ML12110A223
| ML12110A223 | |
| Person / Time | |
|---|---|
| Site: | Limerick  |
| Issue date: | 02/28/2012 |
| From: | Exelon Nuclear |
| To: | Office of Nuclear Reactor Regulation |
| References | |
| Download: ML12110A223 (481) | |
Text
Limerick Generating Station Units 1 & 2 License Renewal Project Environmental Report Response to Request for Additional Information (RAI) for the Review of LGS LRA ER, Dated February 28, 2012 Enclosure 2 Book 2 of 11
E2-6: Enclosure 2: Aquatic Ecology, item D NAI (Normandeau Associates, Inc.). 2010d. Letter from Normandeau Associates, Inc. to Exelon Nuclear via email. Zebra mussel/Asiatic clam Survey. November. PECO (Philadelphia Electric Company). 1984. Environmental Report - Operating License Stage. Limerick Generating Station Units 1&2. 5 vols.
Exelon Response In an email message dated March 23, 2012, the NRC License Renewal Environmental Project Manager clarified that NRC staff is requesting only the sections pertinent to aquatic ecology from the PECO 1984 Environmental Report - Operating License Stage.
The requested documents (NAI 2010d and aquatic ecology excerpts from PECO 1984) are being provided.
Z- NORMANDEAU ASSOCIATES, INC.
S400 Old Reading Pike, Building A, Suite 101 Stowe PA 19464 (610) 705-5733 (610) 705-5739 (Fax) www.normnandeau.com 11 November 2010 Gregory Sprissler Exelon Nuclear Limerick Generating Station P.O. Box 2300 Pottstown, PA 19464 VIA EMAIL: Gregorv.sprissler@exeloncorp.com
SUBJECT:
Zebra mussel/Asiatic clam Survey Normandeau Project No. 20601.004
Dear Mr. Sprissler:
Based on my investigations conducted in the Schuylkill River on 9 September and in the Perkiomen Creek on 3 November, both survey reaches are free of zebra mussel. The Schuylkill River continues to support a large population of Asiatic clam. However, Asiatic clam numbers seem reduced in the Perkiomen Creek. Details of these investigations follow.
Weather conditions were good for both surveys, with little or no rain observed during the previous several days. Water level in the Schuylkill River and in the Perkiomen Creek was sufficiently low to conduct the work with no difficulty. Discharge measured by the USGS in the Schuylkill River at Pottstown was 531 cubic feet per second (cfs) on 9 September and in the Perkiomen Creek at Graterford was 114 cfs on 3 November. The water was clear, allowing inspection of submerged surfaces.
I searched the Schuylkill River at two locations - a point approximately 200 yards upstream of the LGS intake and a point immediately upstream of the now-dismantled Sanatoga Road Bridge, approximately 0.5 miles upstream of the LGS intake. Two locations in the Perkiomen Creek also were searched - directly at the Diversion intake and at the Plank Road Bridge in Central Perkiomen Valley Park, approximately 1.5 miles upstream of the Diversion intake.
On 20 April, I had placed ten 6 inch x 6 inch unglazed clay tiles on the river bottom at each of the four locations. These tiles would provide colonization surfaces for attachment of zebra mussels, if the species is present, until their recovery for inspection in the fall.
All four locations were waded. I:
- Searched for and recovered relatively few of the colonization tiles at the locations. We were able to recover six of the colonization tiles in the Schuylkill River upstream of the Sanatoga Road Bridge and seven in the Perkiomen Creek at the Diversion intake. None Bedford, NH, Corporate Norfolk, CT Hanover,MA Haverstraw,NY Aiken, SC Lewes, DE Hampton, NH Drumore, PA Stevenson, WA Yarmouth, ME Westmoreland, NH Stowe, PA Verona, WI An Employee-owned Company An Equal OpportunityEmployer
NORMANDEAU ASSOCIATES, INC.
Mr. Gregory Sprissler I1 November 2010 Page 2.
were recovered at the other locations. It is my opinion that the missing tiles were washed away due to high river flows, although I cannot discount vandalism. Nevertheless, loss of these tiles did not jeopardize the monitoring effort.
- Viewed the river bottom looking for evidence of zebra mussels attached to the surface of rocks and debris;
- Picked up small rocks and examined them closely; and
- Searched for accumulations of empty zebra mussel and Asiatic clam shells as well as living Asiatic clams.
We saw no living zebra mussels attached to any surface, noting that young-of-the-year individuals could be as small as only several millimeters, nor did we see any empty shells. In the case of Asiatic clam, we saw many empty shells in the Schuylkill River and in the Perkiomen Creek. Unlike last year when we saw many living Asiatic clam in the Perkiomen Creek, we saw very few this year. Coincidentally, many of the empty shells that we saw in the Perkiomen Creek this year appeared in very good physical condition, suggesting recent mortality.
We identified living Asiatic clam in the Schuylkill River, including many 12-15 mm individuals likely one year old. We saw no evidence of recent mortality as we had seen in the Perkiomen Creek. This difference between the Perkiomen Creek and the Schuylkill River is unexplained.
I believe that this letter report provides the information that you need with respect to these two species and LGS source waters. I might add that we will deploy plate samplers in the Schuylkill River and the Perkiomen Creek next spring in order to monitor possible zebra mussel colonization through the warmer months, unless you direct us otherwise.
Please do not hesitate to contact me with any questions. I thank you for the opportunity to conduct this work.
Sincerely, William S. Ettinger Project Manager mke cc: Paul Harmon, Normandeau Associates
Environmental Report Operating License Stage Limerick -Generating Station Units 1 E 2 PHILADELPHIA ELECTRIC COMPANY Vol. 1
THIS EROL SET HAS BEEN UPDATED TO INCLUDE REVISIONS THROUGH Q0 DATED 9/84 .
LGS EROL
SUMMARY
TABLE OF CONTENTS Section Title Volume 1 PURPOSE OF LIMERICK GENERATING STATION AND ASSOCIATED TRANSMISSION ............................. I 1.1 System Demand and Reliability .................. I 1.2 Another Objective .............................. I 1.3 Consequences of Delay .......................... I
- 1. 1A Conservation of Energy Programs ................ I
- 1. 1B Energy Forecasting Methodology ................. I
- 1. 1C Annual Peak Demand Forecasting Method .......... I 2 THE SITE AND ENVIRONMENTAL INTERFACES ............... I 2.1 Geography and Demography ....................... I 2.2 Ecology ........................................ I 2.3 Meteorology ..................................... II 2.4 Hydrology ....................................... II 2.4A Appendix 2.4A - DRBC Approval .................. II 2.5 Geology ......................................... II 2.6 Regional Historic, Archaeological, and Natural Features ............................... II 2.7 Noise .......................................... II 3 THE STATION 3.1 External Appearance ............................ II 3.2 Reactor and Steam-Electric System .............. II 3.3 Station Water Use ............................... II 3.4 Heat Dissipation System ........................ II 3.5 Radwaste Systems and Source Term ............... II 3.6 Chemical and Biocide Wastes .................... II 3.7 Sanitary and Other Waste Systems ............... II i
LGS EROL Section Title Volume 3.8 Reporting of Radioactive Material Movement ..... II 3.9 Transmission Facilities ........................ II 4 ENVIRONMENTAL EFFECTS OF SITE PREPARATION, STATION CONSTRUCTION, AND TRANSMISSION FACILITY CONSTRUCTION ......................................... III 4.1 Site Preparation and Station Construction ...... III 4.2 Transmission Facilities Construction ........... III 4.3 Resources Committed During Construction ........ III 4.4 Radioactivity .................................. III 4.5 Construction Impact Control Programs ........... III 5 ENVIRONMENTAL EFFECTS OF STATION OPERATION .......... III 5.1 Effects of Operation on Heat Dissipation System .......................................... III 5.2 Radiological Impact from Routine Operation.....III 5.2A Radiological Dose Model - Liquid Effluent ...... III 5.2B Radiological Dose Model - Gaseous Effluent ..... III 5.2C 50-Mile Population and Contiguous Population Dose Model ..................................... III 5.3 Effects of Chemical and Biocide Discharges ..... III 5.4 Effects of Sanitary Waste Discharges ........... III 5.5 Effects of Operation and Maintenance of the Transmission Systems ........................... III 5.6 Other Effects .................................. III 5.7 Resources Committed ............................ III 5.8 Decommissioning and Dismantling ................ III 5.9 The Uranium Cycle .............................. III ii
LGS EROL Section Title Volume 6 EFFLUENT AND ENVIRONMENTAL MEASUREMENTS AND MONITORING PROGRAMS .................................. III 6.1 Applicant's Preoperational Environmental Programs ....................................... III 6.2 Applicant's Proposed Operational Monitoring Program ........................................ III 6.3 Related Environmental Measurement and Monitoring Programs ............................. III 6.4 Preoperational Environmental Radiological Monitoring Data ................................ III 7 ENVIRONMENTAL EFFECTS OF ACCIDENTS .................. IV 7.1 Station Accidents Involving Radioactivity ...... IV IJ 7.2 Transportation Accidents Involving Radioactivity .................................. IV 7.3 Other Accidents ................................ IV 8 ECONOMIC AND SOCIAL EFFECTS OF STATION CONSTRUCTION AND OPERATION .......................... IV 8.1 Benefits ....................................... IV 8.2 Costs .......................................... IV 9 ALTERNATIVE ENERGY SOURCES AND SITES ................ IV 10 STATION DESIGN ALTERNATIVES ......................... IV 10.1 Alternative Circulating Systems ................ IV 10.2 Alternative Intake Systems ..................... IV 10.3 Alternative Discharge Systems .................. IV 10.4 Alternative Chemical Waste Systems ............. IV 10.5 Alternative Biocide Treatment Systems .......... IV 10.6 Alternative Liquid Radwaste Systems ............ IV 10.7 Alternative Liquid Radwaste Systems ............ IV 10.8 Alternative Gaseous Radwaste Systems ........... IV iii REV. 1, 9/81
LGS EROL Section Title Volume 10.9 Alternative Transmission Facilities ............ IV 11
SUMMARY
BENEFIT-COST ANALYSIS ....................... IV 11.1 Benefits ........................................ IV 111.2 Costs Incurred .................................. IV 11.3 Conclusions ..................................... IV 12 ENVIRONMENTAL APPROVALS AND CONSULTATIONS ........... IV 13 REFERENCES .......................................... IV
.A ENVIRONMENTAL TECHNICAL SPECIFICATIONS .............. IV iv
LGS EROL CHAPTER 2 THE SITE AND ENVIRONMENTAL INTERFACES TABLE OF CONTENTS Section Title 2.1 GEOGRAPHY AND DEMOGRAPHY 2.1.1 Site Location and Description 2.1.1.1 Specification of Location 2.1.1.2 Site Area 2.1.1.3 Boundaries for Establishing Effluent Release Limits 2.1.2 Population Distribution 2.1.2.1 Population Within 10 Miles 2.1.2.2 Population Between 10 and 50 Miles 2.1.2.3 Transient Population 2.1.2.4 Age Distribution 2.1.3 Use of Adjacent Lands and Waters 2.1.3.1 Industries 2.1.3.2 Transportation Routes 2.1.3.3 Recreational Areas 2.1.3.4 Agricultural Land Use 2.1.3.5 Residences 2.1.3.6 Surface Water Use 2.1.3.7 Groundwater Use 2.2 ECOLOGY 2.2.1 Terrestrial Ecology 2.2.1.1 Flora 2.2.1.1.1 Species Inventory 2.2.1-.1.2 Community Description 2.2.1.1.3 Important Species 2.2.1.2 Amphibians and Reptiles 2.2.1.3 Birds 2.2.1.3.1 Species Inventory 2.2.1.3.2 Community Description 2.2.1.3.3 Important Species 2.2.1.4 Mammals 2.2.1.5 Trophic Relationships 2.2.2 Aquatic Ecology 2.2.2.1 Schuylkill River 2.2.2.1.1 Water Quality and Environmental Stress 2.2.2.1.2 Phytoplankton 2.2.2.1.3 Periphyton 2.2.2.1.4 Macrophytes 2-i Rev. 15, 08/83
LGS EROL TABLE OF CONTENTS (Cont'd)
Section Title 2.2.2.1.5 Zooplankton 2.2.2.1.6 Macroinvertebrates 2.2.2.1.7 Fish 2.2.2.1.8 Trophic Relationships 2.2.2.2 Perkiomen Creek 2.2.2.2.1 Water Quality'and Environmental Stress 2.2.2.2.2 Phytoplankton 2.2.2.2.3 Periphyton 2.2.2.2.4 Macrophytes 2.2.2.2.5 Zooplankton 2.2.2.2.6 Macroinvertebrates 2.2.2.2.7 Fish 2.2.2.2.8 Trophic Relationships 2.2.2.3 East Branch Perkiomen Creek 2.2.2.3.1 Water Quality and Environmental Stress 2.2.2.3.2 Phytoplankton 2.2.2.3.3 Periphyton 2.2.2.3.4 Macrophytes 2.2.2.3.5 Zooplankton 2.2.2.3.6 Macroinvertebrates 2.2.2.3.7 Fish 2.2.2.3.8 Trophic Relationships 2.2.3 Farm Crops, Cows, and Goats 2.2.4 References 2.3 METEOROLOGY 2.3.1 Regional Climatology 2.3.1.1 General Climate 2.3.1.1.1 Air Masses and Synoptic Features 2.3.1.1.2 General Airflow 2.3.1.1.3 Temperature 2.3.1.1.4 Relative Humidity 2.3.1.1.5 Precipitation 2.3.1.1.6 Relationship Between Synoptic and Local Scale Meteorology 2.3.1.2 Seasonal and Annual Frequencies of Severe Weather Phenomenon 2.3.1.2.1 Hurricanes 2.3.1.2.2 Tornadoes 2.3.1.2.3 Thunderstorms and Lightning 2.3.1.2.4 Hail 2.3.1.2.5 Ice Storms and Freezing Rains 2.3.1.2.6 Peak Winds 2.3.1.3 Regional Air Quality 2.3.1.3.1 Summary of Regional Air Quality Data 2-ii Rev. 15, 08/83
LGS EROL TABLE OF CONTENTS (Cont'd)
Sect ion Title 2.3.1.4 References 2.3.2 Local Meteorology 2.3.2.1 Normal and Extreme Values of the Meteorological Parameters 2.3.2.1.1 Wind Direction and Speed 2.3.2.1.2 Atmospheric Stability 2.3.2.1.3 Temperature 2.3.2.1.4 Precipitation 2.3.2.1.5 Humidity 2.3.2.1.6 Fog 2.3.2.2 Topography 2.3.2.3 References 2.4 HYDROLOGY 2.4.1 Surface Water Hydrology 2.4.2 Groundwater Hydrology 2.4.2.1 Historic Floods 2.4.2.2 Low Streamflows 2.4.2.3 Perkiomen Creek and Delaware River Flows 2.4.3 Water Levels 2.4.3.1 Schuylkill River 2.4.3.2 Perkiomen Creek 2.4.3.3 East Branch of Perkiomen Creek 2.4.3.4 Delaware River 2.4.4 Hydrologic Description of the Site Environment 2.4.5 Surface Water Users 2.4.6 Plant Water Requirement 2.4.7 Water Quality 2.4.7.1 Chemical Characteristics of Surface Water Bodies 2.4.7.2 Water Temperature 2.4.7.3 Sediment Characteristics 2.4.8 Water Impoundments 2.4.9 Conclusion 2.4.10 Ground Water Hydrology 2.4.10.1 Description of Aquifers 2.4.10.2 Site Ground Water Occurrence 2.4.10.2.1 Aquifer Parameters 2.4.10.2.2 Water Quality 2.4.10.2.3 Ground Water Levels and Fluctuations 2.4.10.2.4 Directions of Groundwater Flow 2.4.10.2.5 Seepage From the Spray Pond 2.4.11 References 2.4A Appendix 2.4A 2-iii Rev. 3, 03/82
LGS EROL TABLE OF CONTENTS (Cont'd)
Section Title 2.5 GEOLOGY 2.6 REGIONAL HISTORIC, ARCHAEOLOGICAL, AND NATURAL FEATURES 2.7 NOISE 2-iv Rev. 15, 08/83
LGS EROL CHAPTER 2 TABLES Table No. Title 2.1-1 Population Distribution, 0-10 Miles, 1970 2.1-2 Population Distribution, 0-10 Miles, 1980 2.1-3 Population Distribution, 0-10 Miles, 1983 2.1-4 Population Distribution, 0-10 Miles, 1990 2.1-,5 Population Distribution, 0-10 Miles, 2000 2.1-6 Population Distribution, 0-10 Miles, 2010 2.1-7 Population Distribution, 0-10 Miles, 2020 2.1-8 Population Distribution, 10-50 Miles, 1970 2.1-9 Population Distribution, 10-50 Miles, 1980
- 2. 1-10 Population Distribution, 10-50 Miles, 1983 2.1-11 Population Distribution, 10-50 Miles, 1990 2.1-12 Population Distribution, 10-50 Miles, 2000 2.1-13 Population Distribution, 10-50 Miles, 2010 2.1-14 Population Distribution, 10-50 Miles, 2020 2.1-15 Sources of Projected Populations 2.1-16 Bureau of Census Populations of Counties Within 50 Miles of the Site 2.1-17 Industries Within 5 Miles of Site 2.1-18 Present Land Usage Within 5 Miles of LGS 2.1-19 Projected Land Usage Within 5 Miles of LGS 2.1-20 Hooker Chemical Company 2.1-21 Pipelines Within 5 Miles of LGS 2.1-22 Airports Within 10 Miles of the Site 2-v Rev. 4, 07/82
LGS EROL TABLES (Cont'd)
Table No. Title 2.1-23 Airways Within 10 Miles of the Site 2.1-24 Location of Nearest Milk Cow, Milk Goat, Residence, Site Boundary, and Vegetable Garden
- 2. 1-25A Location of Dairy Pastures Within 5 Miles of LGS and Grazing Factors at Each Location
- 2. 1-25B Location of Beef Pastures Within 5 Miles of LGS
- 2. 1-25C Location of Sheep Pastures Within 5 Miles of LGS
- 2. 1-25D Location of Swine Pastures Within 5 Miles of LGS
- 2. 1-25E Location of Goat Pastures Within 5 Miles of LGS 2.1-26 Milk Destination/Production 0-5 Miles From LGS 2.1-27 Distribution of Milk for Pennsylvania 2.1-28 Annual Milk Production Within 50 Miles of LGS 2.1-29 Annual Meat Production Within 50 Miles of LGS 2.1-30 Annual Chicken Production Within 50 Miles of LGS 2.1-31 Annual Vegetable Production Within 50 Miles of LGS.
2.1-32 Annual Fruit Production Within 50 Miles of LGS 2.1-33 Annual Grain Production Within 50 Miles of LGS 2.1-34 Annual Silage Corn Production Within 50 Miles of LGS 2.1-35 Annual Production of All Hay Within 50 Miles of LGS 2.1-36 Crop Production and Yield Summary 2.1-37 Location of Residences Within 1 Mile of LGS 2.1-38 Schuylkill River - Municipal Water Suppliers Down-stream of Limerick Site 2.1-39 Schuylkill River - Industrial Water Users Downstream of Limerick Site 2vi
LGS EROL TABLES (Cont'd)
Table No. Title 2.1-40 Accessible Recreational Areas on the Schuylkill River Downstream of the LGS Site 2.1-41 Accessible Recreational Areas of the Schuylkill River Downstream of the LGS Site (Projected) 2.1-42 Boating Hours on the Schuylkill River Downstream of the LGS Site 2.1-43 Present and Projected Fishing Hours and Edible Fish Catch in the Schuylkill River Downstream of the LGS Site 2.1-44 Percentage of Fish Species Most Frequently Caught in the Vicinity of the LGS Site 2.2-1 Terrestrial Vascular Plants Found on the LGS Site from 1972 through 1978 2.2-2 Amphibians and Reptiles Found on the LGS Site from 1972 through 1978 2.2-3 Sampling History for Ecological Studies of Birds on the LGS Site 2.2-4 Birds Found Within an 8-km Radius of LGS From 1972 to 1978 2.2-5 Important Bird Species Selected for the LGS Site and Criteria for Selection 2.2-6 Mammals Found on the LGS Site from 1972 to 1979 2.2-7 Summary of Collections Made From the Schuylkill River, Perkiomen Creek, and East Branch Perkiomen Creek, by Program and Year 1971-1978 2.2-8 Number of Samples by Year, Program, and Site Collected From the Schuylkill River, 1971 through 1977 2.2-9 Number of Samples by Month, Program, and Collected From the Schuylkill River Near LGS, 1971 through 1977 2.2-10 Listing of Phytoplankton Taxa with Quarterly (Seasonal)
Densities per Taxa Collected from Station S77720, Schuylkill River, Limerick Generation Station, 1974 2vii
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-11 Periphyton Production Listed as Total Biomass (Standing Crop) (mg/dM2 ) and Total Productivity Rates (mg/dm2 /day-l) 2.2-12 Species List and Relative Abundance of Aquatic Macrophytes in the Vicinity of LGS, Observed in 1977 2.2-13 Species List and Relative Abundance of Aquatic Macroinvertebrates Collected by All Methods from the Schuylkill River, 1970 through 1976 2.2-14 Numerical Summary Data on Important Species (taxa) of Benthic Macroinvertebrates Collected in Quantitative Samples (1972-1976) from the Schuylkill River 2.2-15 Biomass of Important Benthic Macroinvertebrates Collected in Quantitative Samples (1972-1974) from the Schuylkill River 2.2-16 Monthly Densities (Mean Number per Square Meter) of Important Species (Taxa) of Benthic Macroinvertebrates, Collected from the Schuylkill River, 1972 through 1976 2.2-17 Monthly Densities of Important Species (Taxa) of Benthic Macroinvertebrates Collected from the Schuylkill River, 1972 through 1974 2.2-18 Total Number of Species (Taxa) of Benthic Macro-invertebrates Collected per Sample from the Schuylkill River Near LGS 1973 through 1976 2.2-19 Monthly Percent Composition of Dominant Drift Species (Taxa) of Macroinvertebrates Collected from the Schuylkill River at S77568, 1972 through 1975 2.2-20 Monthly Densities of Selected Species (Taxa) of Macroinvertebrates Collected in Drift Samples from S77560 in the Schuylkill River, 1972 through 1975 2.2-21 Monthly Estimates of the Percent of Benthos Drifting in the Schuylkill River near Limerick Generating Station, 1972 through 1975 2viii
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-22 Fish and Hybrids Collected in the Vicinity of Limerick Generating Station, Schuylkill River, 1970 through 1976 2.2-23 Mean Density and Relative Abundance of Selected Larval Fish Collected from the East Channel of the Schuylkill River at S77560, May-August 1974 and 1975 2.2-24 Horizontal Variation in Density of Larval Fish Collected from the Schuylkill River at S77560 in 1975 2.2-25 Total Catch and Relative Abundance of Larval Fish Collected by Trap Net from the Schuylkill River Shoreline at S77560, May through August 1975 2.2-26 Total Number and Percent Catch of Shoreline Larval Fish Sampled by Push Net from the Schuylkill River During the Spawning Period in 1976 2.2-27 Total Number and Catch per Effort of Larval Fish Collected by Push Net in the Schuylkill River Near Limerick Generating Station, in 1976 2.2-28 Total Catch, Relative Abundance, and Frequency of Occurrence (FO%) of Fish Collected by Seine from the Schuylkill River (all Sites Combined) in 1975 and 1976 2.2-29 Monthly Variation in Total Catch and Relative Abundance of Important Species of Fish and Total Number of Species Collected by Seine from the Schuylkill River (all Sites Combined), 1975 and 1976 2.2-30 Spatial Variation in Total Catch and Relative Abundance of Important Species of Fish and Total Number of Species Collected by Seine from the Schuylkill River, 1975 and 1976 2.2-31 Total Catch and Relative Abundance of Small Fish Collected from the Schuylkill River Near LGS, 1973 through 1976 2.2-32 Total Catch and Relative Abundance of Fish and Hybrids Collected During Large Fish Population Estimate Sampling, 1973 through 1975 2ix
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-33 Total Catch and Relative Abundance of Fish Collected During Catch-per-Unit-Effort Sampling, July through December 1976 2.2-34 Fish Taken by Trap Net From the Schuylkill River at Vincent Pool From May 1971 through December 1976 2.2-35 Criteria for Determining Important Fish of the Schuylkill River 2.2-36 Spatial and Temporal Variation in Catch-per-Unit-Effort (no./min of Electrofishing x100) of Important Species Collected from the Schuylkill River Near Limerick Generating Station July through December 1976 2.2-37 Estimated Number and Biomass of Selected Important Species Collected from the Schuylkill River During Large Fish Population Estimate Sampling, 1973 through 1977 2.2-38 Mean Calculated Fork Length at Annulus for Selected Important Species Collected from the Schuylkill River Near Limerick Generating Station, 1973 through 1975 2.2-39 Length-Weight Relationships for Selected Important Fish Species collected from the Schuylkill River near Limerick Generating Station, 1973 through 1978 2.2-40 Number of Samples Collected by Year, Program, and Site Collected from Perkiomen Creek, 1972 through 1977 2.2-41 Number of Samples by Month, Program, and Year Collected from Perkiomen Creek, 1972 through 1977 2.2-42 Monthly Qualitative Listing of Phytoplankton Genera Collected at P14390 in Perkiomen Creek in 1974 2.2-43 Periphyton Production Listed as Total Biomass (Standing Crop) mg/dm2 and Total Productivity Rates mg/dm2 /day 2.2-44 Species List and Relative Qualitative Abundance of Macroinvertebrates Collected by all Methods from 2x
LGS EROL TABLES (Cont'd)
Table No. Title all Habitats in East Branch Perkiomen Creek and Perkiomen Creek, 1970 through 1976 2.2-45 Selected Measurements for Total Macrobenthos in the Riffle Biotope of Perkiomen Creek and East Branch Perkiomen Creek (1972-1976) 2.2-46 Mean Density (no./m 2 ), Percent Composition (%), and Frequency Of Occurence (FO%) of Benthic Macroinvertebrates Collected in Quantitative Samples (1972-1976) from The Riffle Biotope of East Branch Perkiomen Creek, all Stations Combined 2.2-47 Mean Density (mg/M 2 ), Percent Composition (%), and Frequency of Occurence (FO%) of Benthic Macroinvertebrates Collected in Quantitative Samples from the Riffle Biotope of East Branch Perkiomen Creek, all Stations Combined 2.2-48 Monthly Densities (Mean no./m 2 ) of Important and Total Taxa of Benthic Macroinvertebrates, Collected from East Branch Perkiomen Creek and Perkiomen Creek, all Stations and Years Combined, 1972-1976 2.2-49 Spatial Distribution, by Station, by Year, of Important Benthic Macroinvertebrates Collected in Quantitative Samples (1972-1976) from the Riffle Biotope of East Branch Perkiomen Creek and Perkiomen Creek 2.2-50 Spatial Distribution, by Station by Year, of Important Benthic Macroinvertebrates Collected in Quantitative Samples (1973, 1974) from the Riffle Biotope of East Branch Perkiomen Creek and Perkiomen Creek 2.2-51 Summary Table of Aquatic Macronivertebrate Drift as Measured for Each Monthly 24-Hour Study in East Branch Perkiomen Creek and Perkiomen Creek 2.2-52 Diel Periodicity of Aquatic Drift on East Branch Perkiomen Creek and Perkiomen Creek Expressed as a Percent of the 24-hour Total, All Drift Studies Combined 2xi
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-53 Fish Collected in Perkiomen Creek by all Types of Gear During the Period June 1970 through December 1977 2.2-54 Mean Density and Relative Abundance of Drifting Larval Fish Collected from Perkiomen Creek at P14390, May through August, 1973, 1974 and 1975 2.2-55 Total Catch and Relative Abundance of Larval Fish Collected by Trap Net from Perkiomen Creek Shoreline at P14390, May through August 1975 2.2-56 Daily Mean Density (no./m') of Drifting Larval Fish Collected from Perkiomen Creek at P14390, May through August, 1974 and 1975 2.2-57 Horizontal Variation in Density of Larval Collected from Perkiomen Creek at P14390 in 1975 2.2-58 Mean Drift Density of Larval Fish in the East and West Channels of Perkiomen Creek at P14390 in 1975 2.2-59 Annual and Spatial Variation in Mean Catch-per-Unit-Effort (C/F and Relative Abundance of Fish Collected by Seine from the Perkiomen Creek in 1975 and 1976) 2.2-60 Annual Variation and Frequency of Occurrence (FO) in Age 0 Sunfish Species Collected by Electrofishing in Perkiomen Creek (all Sites Combined) in 1975 and 1976 2.2-61 Monthly Variation in Mean Catch-per-Unit-Effort of Fish Collected by Seine from Perkiomen Creek (all Sites Combined) in 1975 and 1976 2.2-62 Total Catch and Relative Abundance of Fish Collected by Electrofishing from Perkiomen Creek in 1974, 1975 and 1976 2.2-63 Criteria for Determination of Important Fish of Perkiomen Creek 2.2-64 Annual and Spatial Variation in Redbreast Sunfish Population Estimates at Four Sites on Perkiomen Creek in 1975 and 1976 2xii
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-65 Population Estimates (Number per Hectare) and Estimated Biomass (weight per Hectare) of Large Fish Collected by Electrofishing from Four Sites, on Perkiomen Creek in 1974, 1975, and 1976 2.2-66 Population Estimates by Age-Group for Redbreast Sunfish Collected from Four Sites on Perkiomen Creek in 1974, 1975, and 1976 2.2-67 Length-Weight Relationships of Important Species Collected by Seine from Perkiomen Creek in 1975 and 1976 2.2-68 Mean Calculated Lengths at Annulus for Redbreast Sunfish, White Sucker, and Smallmouth Bass Collected From Perkiomen Creek in 1973 and 1976 2.2-69 Length-Weight Relationships for White Sucker Collected by Electrofishing at Four Sites on Perkiomen Creek in 1976 2.2-70 Number of Samples by Year, Program, and Site Collected from East Branch Perkiomen Creek, 1972 through 1977 2.2-71 Number of Samples by Month, Program, and Year Collected from East Branch Perkiomen Creek, 1972 through 1977 2.2-72 Periphyton Standing Crop Biomass (mg/dm2 ) in Ash-free dry Weight and Productivity Rates (mg/dm2 /day) in Ash-free Dry Weight by Station in East Branch Perkiomen Creek, 1973 and 1974 2.2-73 Fish Collected in the East Branch Perkiomen Creek by all Types of Gear during the Period of June 1970 through December 1976 2.2-74 Mean Density and Relative Abundance of Drifting Larval Fish Collected from East Branch Perkiomen Creek at E2650, May-August in 1973 and 1974 2.2-75 Mean Daily Drift Density (no./m 3 ) for Selected Larval Fish Collected from East Branch Perkiomen Creek at E2650, 1973 and 1974 2xiii
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-76 Mean Catch-per-Unit-Effort (C/F) and Relative Abundance of Fish Species Collected by Seine from East Branch Perkiomen Creek in 1975 and 1976 2.2-77 Relative Abundance (%N) and Biomass (%W) of Fish Collected by Electrofishing from Lotic Sites, East Branch Perkiomen Creek, 1973 and 1975 2.2-78 Relative Abundance (% Total Catch) of all Species Collected by Electrofishing From Fretz (E15500) and WaWa (F5650) Reservoirs, East Branch Perkiomen Creek in 1974 and 1975 2.2-79 Criteria for Determination of Important Fish of East Branch Perkiomen Creek 2.2-80 Population Estimates and Estimated Biomass of Selected Species Collected by Electrofishing from Lotic Sites, East Branch Perkiomen Creek, 1973 and 1975 2.2-81 Population Estimates and Estimated Biomass of Selected Species Collected by Electrofishing from Lentic Sites, East Branch Perkiomen Creek, 1974 and 1975 2.2-82 Length-Weight Relationships of Selected Species Collected by Seine from East Branch Perkiomen Creek in 1975 and 1976 2.2-83 Length-Weight Relationships of Selected Species Collected by Electrofishing from Lotic Sites, East Branch Perkiomen Creek, 1973 and 1975 2.2-84 Mean Calculated Lengths at Annulus for Redfin Pickerel Collected at Five Sites on the East Branch Perkiomen Creek in 1973 and 1975 2.2-85 Mean Calculated Lengths at Annulus for White Sucker Collected by Electrofishing Upstream and Downstream of Sellersville, East Branch Perkiomen Creek, in 1973 2.2-86 Mean Calculated Lengths at Annulus for Redbreast Sunfish Collected by Electrofishing from Lotic Sites, East Branch Perkiomen Creek, in 1973 and 1975 2xiv
LGS EROL TABLES (Cont'd)
Table No. Title 2.2-87 Mean Calculated Lengths at Annulus for Green Sunfish Collected by Electrofishing from Lotic Sites, East Branch Perkiomen Creek, in 1973 and 1975 2.2-88 1976 Total Wheat Production Within 5 Miles of LGS--
Summary in Acres by Sector and Distance 2.2-89 1976 Total Grain Core Production Within 5 Miles of LGS--Summary in Acres by Sector and Distance 2.2-90 1976 Total Corn (Silage) Production Within 5 Miles of LGS--Summary in Acres by Sector and Distance 2.2-91 1976 Total Alfalfa, Timothy, and Clover Within 5 Miles of LGS--Summary in Acres by Sector and Distance 2.2-92 1976 Total Production (all Crops) Within 5 Miles of LGS--Summary in Acres by Sector and Distance 2.2-93 1976 Total Cow Population Within 5 Miles of LGS by Sector and Distance 2.2-94 Total Goat Population Within 5 Miles of LGS by Sector and Distance 2.3.1-1 Comparison of Annual Wind Direction Frequency Distributions (%)
2.3.1-2 Mean Monthly Temperature Comparison (OF) 2.3.1-3 Comparison of Mean Morning and Afternoon Relative Humidity (%)
2.3.1-4 Distribution of Precipitation, Philadelphia International Airport 2.3.1-5 Distribution of Precipitation, Allentown Airport 2.3.1-6 Mean Number of Thunderstorms, Days per Year 2.3.1-7 Fastest Mile of Wind 2.3.1-8 Applicable State Federal Ambient Air Quality Standards 2xv
LGS EROL TABLES (Cont'd)
Table No. Title 2.3.1-9 Summary of South East Pennsylvania Air Basin Air Quality Data 2.3.1-10 Summary of COPAMS, Air Quality Data 2.3.2-1 LGS Percent Data Recovery for Meteorological Sensors 2.3.2-2(l) Weather Station No. 1, Annual Wind Distribution by Brookhaven Turbulence Class, January 1972 to December 1976 2.3.2-3(l) Weather Station No. 1, Monthly Wind Distribution by Brookhaven Turbulence Class, January 1972 to December 1976 2.3.2-4(t) Weather Station No. 1, Annual Wind Distribution by NRC Lapse Rate Stability Class, 266-26 ft. Height Interval, January 1972 to December 1976 2.3.2-5(l) Weather Station No. 1, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 226-26 ft. Height Interval, January 1972 to December 1976 2.3.2-6(l) Weather Station No. 1, Annual Wind Distribution by NRC Lapse Rate Stability Class, 171-26 ft. Height Interval, January 1972 to December 1976 2.3.2-7(l) Weather Station No. 1, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 171-26 ft. Height Interval, January 1972 to December 1976 2.3.2-8(l) Weather Station No. 1, Annual Wind Distribution by Brookhaven Turbulence Class, April 1972 to March 1973 2.3.2-9(l) Weather Station No. 1, Monthly Wind Distribution by Brookhaven Turbulence Class, April 1972 to March 1973 2.3.2-10(1) Weather Station No. 1, Annual Wind Distribution by NRC Lapse Rate Stability Class, 266-26 ft. Height Interval, April 1972 to March 1973 2.3.2-11 Weather Station No. 1, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 266-26 ft. Height Interval, April 1972 to March 1973 2xvi
LGS EROL TABLES (Cont'd)
Table No. Title 2.3.2-12(l) Weather Station No. 1, Annual Wind Distribution by NRC Lapse Rate Stability Class, 171-26 ft. Height Interval, April 1972 to March 1973 2.3.2-13(l) Weather Station No. 1, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 171-26 ft. Height Interval, April 1972 to March 1973 2.3.2-14(l) Weather Station No. 2 Annual Wind Distribution by Brookhaven Turbulence Class, April 1972 to March 1973 2.3.2-15(l) Weather Station No. 2, Monthly Wind Distribution by Brookhaven Turbulence Class, April 1972 to March 1973 2.3.2-16(1) Weather Station No. 2, Annual Wind Distribution by NRC Lapse Rate Stability Class, 300-26 ft. Height Interval, April 1972 to March 1973 2.3.2-17(l) Weather Station No. 2, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 300-26 ft. Height Interval, April 1972 to March 1973 2.3.2-18(l) Weather Station No. 2, Annual Wind Distribution by NRC Lapse Rate Stability Class, 155-26 ft. Height Interval, April 1972 to March 1973 2.3.2-19(l) Weather Station No. 2, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 155-26 ft. Height Interval, April 1972 to March 1973 2.3.2-20(l) Satellite Tower, Annual Wind Distribution by Brookhaven Turbulence Class, January 1975 to December 1976 2.3.2-21 Satellite Tower, Monthly Wind Distribution by Brookhaven Turbulence Class, January, 1975 to December 1976 2.3.2-22(l) Satellite Tower, Annual Wind Distribution by NRC Lapse Rate Stability Class, 266-26 ft. Height Interval, January 1975 to December 1976 2.3.2-23(1) Satellite Tower, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 266-26 ft. Height Interval, January 1975 to December 1976 2xvii
LGS EROL TABLES (Cont'd)
Table No. Title 2.3.2-24(L) Satellite Tower, Annual Wind Distribution by NRC Lapse Rate Stability Class, 171-26 ft. Height Interval, January 1975 to December 1976 2.3.2-25(7) Satellite Tower, Monthly Wind Distribution by NRC Lapse Rate Stability Class, 171-26 ft. Height Interval, January 1975 to December 1976 2.3.2-26 Limerick Generating Station Comparison of Annual Wind Direction Frequency Distributions (%) Weather Station No. 1 2.3.2-27 LGS Monthly Average Wind Speeds (mph) Weather Station No. 1 2.3.2-28 LGS Comparison of Annual Wind Direction Frequency Distributions (%) Weather Station No. 1 2.3.2-29 LGS Comparison of Annual Wind Direction Frequency Distributions (%) Weather Station No. 2 2.3.2-30 LGS Comparison of Annual Wind Direction Frequency Distributions (%) from Equivalent Heights LGS Comparison of Annual Wind Direction Frequency 2.3.2-31 Distributions (%) Low Level Sensors 2.3.2-32 LGS Comparison of Monthly Average Wind Speeds (mph) 2.3.2-33(l) Annual Wind Direction Persistence, Weather Station No. 1, January 1972 to December 1976 2.3.2-34(l) Monthly Wind Direction Persistence, Weather Station No. 1, January 1972 to December 1976 2.3.2-35(l) Annual Wind Direction Persistence, Weather Station No. 1, April 1972 to March 1973 2.3.2-36(l) Monthly Wind Direction Persistence, Weather Station No. 1, April 1972 to March 1973 2.3.2-37(t) Annual Wind Direction Persistence, Weather Station No. 2, April 1972 to March 1973 2.3.2-38(l) Monthly Wind Direction Persistence, Weather Station No. 2, April 1972 to March 1973 2xviii
LGS EROL TABLES (Cont'd)
Table No. Title 2.3.2-39 Comparison of Wind Speed Frequency Distributions (%)
2.3.2-40 Annual Frequency Distribution of Brookhaven Turbulence Classes, Weather Station No. 1, January 1972 to December 1976 2.3.2-41 Annual Frequency Distribution of Pasquill Stability Classes, Weather Station No. 1, January 1972 to December 1976 2.3.2-42 Annual Frequency Distribution of Brookhaven Turbulence Classes, Weather Stations No. 1 and 2, April 1972 to March 1973 2.3.2-43 Annual Frequency Distribution of Pasquill Stability Classes, Weather Station No. 1 and 2, April 1972 to December 1973 2.3.2-44 BNL Turbulence Classification 2.3.2-45(7) Annual Temperature Inversion Persistence, Weather Station No. 1, January 1972 to December 1976 2.3.2-46(l) Monthly Temperature Inversion Persistence, Weather Station No. 1, January 1972 to December 1976 2.3.2-47 Annual Temperature Inversion Persistence, Weather Station No. 1, April 1972 to March 1973 2.3.2-48(l) Monthly Temperature Inversion Persistence, Weather Station No. 1, April 1972 to March 1973 2.3.2-49(t) Annual Temperature Inversion Persistence, Weather Station No. 2, April 1972 to March 1973 2.3.2-50(l) Monthly Temperature Inversion Persistence, Weather Station No. 2, April 1972 to March 1973 2.3.2-51 LGS Mean Morning and Afternoon Mixing Heights 2.3.2-52 Monthly and Annual Means and Extremes of Ambient Temperature, Weather Station No. 1, January 1972 to December 1976 2.3.2-53(l) Annual Frequency Distribution of Ambient Temperature, Weather Station No. 1, January 1972 to December 1976 2xix
LGS EROL TABLES (Cont'd)
Table No. Title 2.3.2-54(7) Monthly Frequency Distribution of Ambient Temperature, Weather Station No. 1, January 1972 to December 1976 2.3.2-55(8) Annual Summary of Diurnal Temperature Variation, Weather Station No. 1, January 1972 to December 1976 2.3.2-56(l) Monthly Summary of Diurnal Temperature Variation Weather Station No. 1, January 1972 to December 1976 2.3.2-57 Comparison of Monthly Mean Temperatures, Limerick Versus Philadelphia 2.3.2-58 Comparison of Monthly Mean Temperatures, Limerick Versus Allentown 2.3.2-59 Monthly Precipitation Distribution, Weather Station No. 1, January 1972 to December 1976 2.3.2-60(6) Annual Precipitation Wind Roses by Precipitation Rate Class, Weather Station No. 1, January 1972 to December 1976 2.3.2-61(7) Monthly Precipitation Wind Roses by Precipitation Rate Class, Weather Station No. 1, January 1977 to December 1976 2.3.2-62(l) Annual Precipitation Rate Distribution, Weather Station No. 1, January 1972 to December 1976 2.3.2-63(l) Monthly Precipitation Rate Distribution, Weather Station No. 1, January 1972 to December 1976 2.3.2-64(l) Annual Summary of Precipitation Intensity Versus Duration, Weather Station No. 1, January 1972 to December 1976 2.3.2-65(l) Monthly Composite Summary of Precipitation Intensity Versus Duration, Weather Station No. 1, January 1972 to December 1976 2.3.2-66 Comparison of Monthly Mean Precipitation, Limerick Versus Philadelphia 2.3.2-67 Comparison of Monthly Mean Precipitation, Limerick Versus Allentown 2xx
LGS EROL TABLES (Cont'd)
Table No. Title 2.3.2-68(7 ) Annual Frequency Distribution of Relative Humidity 2.3.2-69(l) Monthly Frequency Distribution of Relative Humidity 2.3.2-70(8) Annual Summary of Diurnal Relative Humidity Variation 2.3.2-71(8) Monthly Summary of Diurnal Relative Humidity Variation 2.3.2-72(8) Annual Frequency Distribution of Absolute Humidity 2.3.2-73(8) Monthly Frequency Distribution of Absolute Humidity 2.3.2-74(8) Annual Summary of Diurnal Absolute Humidity Variation 2.3.2-75(l) Monthly Summary of Diurnal Absolute Humidity Variation 2.3.2-76(l) Annual Frequency Distribution of Dew Point Temperature 2.3.2-77(1) Monthly Frequency Distribution of Dew Point Temperature 2.3.2-78(1) Annual Summary of Diurnal Dew Point Temperature Variation 2.3.2-79(l) Monthly Summary of Diurnal Dew Point Temperature Variation 2.3.2-80(l) Annual Cumulative Frequency Distribution of Wet Bulb Temperature 2.3.2-81(l) Monthly Cumulative Frequency Distribution of Wet Bulb Temperature 2.3.2-82 Comparison of Mean Morning and Afternoon Relative Humidity 2.3.2-83 Comparison of Frequency Distributions of Daily Average Relative Humidity Values 2.3.2-84 Comparison of Annual Frequency Distributions of Hourly Relative Humidity Values 2.3.2-85 Mean Number of Days with Heavy Fog 2.3.2-86 Offsite Elevations Versus Distance from Vent 2.3.2-87 Onsite Elevations Versus Distance from Vent 2.3.2-88(l)
Joint Frequency Distribution of Relative Humidity, Wind Direction, Wind Speed and Atmospheric Stability Class 2.4-1 Principal Tributaries of the Schuylkill River REV. 1, 9/81 2xxi
LGS EROL TABLES (Cont'd)
Table No. Title 2.4-2 Surface Water Gauging Stations Upstream From Limerick Site 2.4-3 Minor Dams Upstream of LGS 2.4-4 Dams on the Schuylkill Downstream of LGS 2.4-5 Major Floods at Selected Stations on the Schuylkill River 2.4-6 Instantaneous and Average Daily Minimum Flows Each Year for the Schuylkill at Pottstown, Pennsylvania, (cfs) 2.4-7 Duration Table of Daily Flow for the Schuylkill River, Perkiomen Creek, and Delaware River (cfs) 2.4-8 Long-Term Average Stream Flows for the Schuylkill River, Perkiomen Creek, and Delaware River 2.4-9 Observed and Estimated Water Surface Elevations of the Schuylkill River at LGS 2.4-10 Domestic Water Users on the Schuylkill River Downstream of Limerick Site 2.4-11 Industrial Water Users on the Schuylkill River Downstream of Limerick Site 2.4-12 Summary of Average (1974-78) Water Quality Data During November Through May for the Schuylkill River 2.4-13 Summary of Average (1974-78) Water Quality Data During June Through October for the Schuylkill River 2.4-14 Summary of East Branch Perkiomen Creek Water Quality, 1975 through 1978 2.4-15 Summary of East Branch Perkiomen Creek Water Quality 1975 through 1978 2.4-16 Water Quality Records of the Delaware River at Trenton, New Jersey 2.4-17 Summary of Schuylkill River Water Temperature at Pottstown, Pennsylvania 2xxii
LGS EROL TABLES (Cont'd)
Table No. Title 2.4-18 Daily Suspended Sediment Discharge of the Schuylkill River at Manayunk, Pennsylvania 2.4-19 Duration Table for Suspended Sediment Concentrations of the Schuylkill River 2.4-20 Permeability Data 2.4-21 Chemical Analyses of Ground Water in the Brunswick Lithofacies in Montgomery County, Pennsylvania 2.4-22 Chemical Analyses of Ground Water From the Wells in the Brunswick Lithofacies at the Limerick Project Site 2.7-1 Ambient Noise Levels From 1973 Survey (1) These tables have been omitted from this report because of the large number of pages.
They are presented in Reference 2.3.2-9.
REV. 1, 9/81 2xxiii
LGS EROL CHAPTER 2 FIGURES Figure No. Title 2.1-1 The General Location of LGS 2.1-2 General Site Area Map 2.1-3 LGS Site Plan 2.1-4 LGS Principal Station Structures 2.1-5 Population Distribution Map Within 10 Miles of LGS 2.1-6 Population Distribution Map Between 10 and 50 Miles of LGS 2.1-7 Industries Within the LPZ 2.1-8 Transportation Routes and Pipelines 2.1-9 Location of Downstream Surface Water Users, Schuylkill River 2.2-1 Principal Plant Communities 2.2-2 Hypothetical Food Web 2.2-3 Study Area 2.2-4 Species Distribution of Dominant Aquatic Macrophytes 2.2-5 Temporal Variation in Larval Fish Drift at S77560, 1974 and 1975 2.2-6 Temporal Variation in Number of Fish Larvae Collected by Push Net, 1976 Number of Fish Species Collected by Seine by Month 2.2-7 and Station 2.2-8 Swallowtail Shiner Seine Catch and Relative Abundance 2.2-9 Spotfin Shiner Seine Catch and Relative Abundance 2.2-10 Brown Bullhead Population Age Structure 2.2-11 Adult Redbreast Sunfish Seasonal Feeding Habits 2xxiv
LGS EROL FIGURES (Cont'd)
Figure No. Title 2.2-12 Mean Population Estimate for Age 0 Redbreast, Green, and Pumpkinseed Sunfish 2.2-13 Pumpkinseed Population Age Structure 2.2-14 Structure and Function of Selected Biotic Components 2.2-15 Perkiomen Creek and East Branch Perkiomen Creek Study Area 2.2-16 Temporal Variation in Larval Fish Drift Density at P14390, for 1973 Through 1975 2.2-17 Monthly Drift Density of Larval Fish Species at P14390 2.2-18 Temporal Variation in Larval Fish Drift Density at E2650 2.2-19 Population Estimates of Redbreast Sunfish at 5 Lotic Sites in 1973 2.2-20 Population Estimates of Redbreast at 5 Lotic Sites in 1975 2.2-21 Population Estimates of Green Sunfish by Age Group at 5 Lotic Sites in 1973 2.2-22 Population Estimates of Green Sunfish by Age Group at 5 Lotic Sites in 1975 2.3.1-1 COPAMS Monitoring Stations 2.3.2-1 Limerick Versus Philadelphia Wind Direction Percentage 2.3.2-2 Limerick Versus Allentown Wind Direction Percentage 2.3.2-3 Limerick Versus Peach Bottom Wind Direction Percentage 2.3.2-4 Philadelphia Versus Philadelphia Wind Direction Percentage 2.3.2-5 Allentown Versus Allentown Wind Direction Percentage at 20 and 270 Feet 2.4-1 Schuylkill River Basin 2xxv
LGS EROL FIGURES (Cont'd)
Figure No. Title 2.4-2 Location of Downstream Surface Water Users 2.4-3 Flood Frequency Curve 2.4-4 Low Flow Frequency Curves - Schuylkill River at Pottstown, Pa.
2.4-4a Low Flow Frequency Curves - Perkiomen Creek at Graterford, Pa.
2.4-4b Low Flow Frequency Curves - Delaware River at Trenton, N. J.
2.4-5 Flow Duration Curve 2.4-6 Rating Curve 2.4-7 Computed Water Surface Profiles 2.4-7a 100-year Floodplain Near Schuylkill Pumping Station 2.4-7b 100-year Floodplain Near Perkiomen Pumping Station 2.4-7c 100-year Floodplain Near Discharge Location of Perkiomen Water Transmission Main - East Branch of Perkiomen Creek 2.4-7d Energy Dissipator Channel, Perkiomen Water Transmission Main - East Branch of Perkiomen Creek 2.4-7e 100-year Floodplain Near Point Pleasant Pumping Station - Delaware River 2.4-8 Consumptive Makeup Water Supply 2.4-9 Cummulative Annual Water Discharges 2.4-1OA Hydrographs of Observation Wells - Spray Pond Area 2.4-lOB Hydrographs of Observation Wells - Power Block Area 2.4-1OC Groundwater Elevations - Daily Precipitation 2.4-11 Observation Wells and Potentiometric Contours of Water Table, May 25, 1979 2.4-12 Flownet for Spray Pond with Semi-impervious Lining 2-xxvi Rev. 3, 03/82
LGS EROL FIGURES (Cont'd)
Figure No. Title 2.7-1 Measuring Points for 1973 Ambient Noise Survey 2-xxvii Rev. 3, 03/82
SECTION 2.2.2, AQUATIC ECOLOGY (264 pages)
LGS EROL during the previous summer. Deer are the most important eastern big game mammal, and are recreationally as well as commercially valuable. They are aesthetically important where abundant, although they can do considerable damage to young orchards and vegetable crops.
2.2.1.5 Trophic Relationships A terrestrial ecosystem comprises numerous food chains and trophic levels. At the first trophic level are the producers, green plants that convert solar energy to biomass and provide cover for numerous organisms. Animal diversity is associated with the stratification and growth forms of plants.
Primary consumers (herbivores) feed on a variety of plant material including leaves, twigs, bark, fruit, and nuts. Common small herbivores in the vicinity of LGS (Figure 2.2-2) are the eastern cottontail rabbit, meadow mouse, muskrat, song sparrow, and grasshopper. The only large herbivore present is the white-tailed deer. Herbivores in turn are an energy source for carnivores (predators), represented on the site by red-backed salamander, black racer, common yellowthroat, and some mammals.
Third-level consumers are represented by the sparrow hawk, osprey, and great horned owl.
Consumers that feed on both plant and animal material are called omnivores. Scavengers occupy this group and their food habits vary with season, food availability, size of organisms, and stage of life cycle. Omnivores near LGS include frogs, turtles, common crows, raccoons, and red foxes.
Decomposers provide the final link in most food chains; they utilize dead plant and animal matter, reducing complex materials into simple substances. Two groups of decomposer organisms are recognized, macroscopic and microscopic. Macroorganisms include earthworms, millipedes, and slugs; microorganisms are primarily bacteria, fungi, and protozoans.
2.2.2 AQUATIC ECOLOGY Aquatic biota in three streams, (Schuylkill River, East Branch Perkiomen Creek, Perkiomen Creek) in the vicinity of LGS was studied by the Applicant's consultant from 1970 through 1978. A summary of sampling history by river system and biotic component is given in Table 2.2-7.
2.2-16
LGS EROL 2.2.2.1 Schuylkill River The temperate warm water of the Schuylkill River meanders 209 km from its source at Tuscarora Springs, Schuylkill County, Pennsylvania, to its confluence with the Delaware River at Philadelphia. The river cuts through portions of the Appalachian Mountain, Great Valley, Reading Prong, Triassic Lowland, Piedmont Upland, and Coastal Plain physiographic regions, and drains 4972 km2 of southeastern Pennsylvania. The river near the plant site (Figure 2.2-3) is productive, and dependent to a large degree on allochthonous sources of energy as it is measureably heterotrophic most of the year.
Extensive environmental degradation has occurred in the Schuylkill in the past. These conditions have adversely affected aquatic biota, and the present community is somewhat depauperate and unstable in comparison with historic records. It is anticipated that future amelioration of existing stresses will result in increased diversity and stability of the Schuylkill River community.
Plant operation will impact the river due to cooling-water withdrawal and discharge. The LGS study area as used in this section refers to the Schuylkill River from U.S. 422 bridge downstream to Vincent Dam. For a further description of this area, refer to Section 6.1. Sample stations are designated by common name, and by the letter 'S' followed by a number that indicates distance in meters from the mouth of the river. Where stations include several meters of stream, site numbers designate the downstream end of the station. Summaries of sampling history for each program are given in Tables 2.2-8 and 9.
2.2.2.1.1 Water Quality and Environmental Stress When the first settlers arrived in the Schuylkill Valley in the 17th century, they found a pure and pristine stream that abounded with many species of fish, including American shad and striped bass. The Schuylkill Valley quickly became a center of development in Pennsylvania, and the river became a major means by which raw materials were transported to Philadelphia. In 1817, the Schuylkill Navigation Company began construction of the Schuylkill Canal which was completed in 1824. The canal operated until 1928, when high maintenance costs and excessive siltation caused its closure.
Commercial coal mining in the upper Schuylkill watershed began about 1824, and the river was used as a convenient and inexpensive place to dump excess mine water and culm. Mine water contained much free sulfuric acid and iron that degraded water 2.2-17
LGS EROL quality as far downstream as Reading, and reduced the waste assimilative capacity of the river. Culm compounded the problem by silting the channel; the decrease in depth rendered the river unsuitable for navigation, and caused downstream flooding.
These conditions persisted until 1945 when the Brunner, or Clean Streams, Act was passed that prohibited discharging wastes into the river. It set as its goal the elimination of pollutant discharges by 1985. The Desilting Act also was passed in 1945 and provided for removal of silt and culm from the Schuylkill from its source at Tuscarora Springs downriver to Norristown.
Twenty-two desilting basins were constructed in this reach, and sediment was pumped from the river into the basins where silt was trapped and the water decanted. Desilting improved the quality of the Schuylkill dramatically. However, as the volume of municipal and industrial wastes increased, water quality once again deteriorated. Further regulation under the Clean Streams Act has resulted in a gradual improvement in water quality since the late 1960's.
The present status of river water quality ranges from poor to good and, according to a recent water quality inventory (Pennsylvania Department of Environmental Resources; p. 40, Ref 2.2-12), the river near LGS has the best water quality. The headwaters continue to be degraded by mine water and raw or poorly treated sewage. This state of degradation persists as far downstream as Reading, at which point the limestone in Maiden and Tulpehocken Creeks enters the Schuylkill and neutralizes the mine acid. Siltation from coal mining remains a problem downstream from Reading, although the rate has decreased with reduced mining activity.
Flooding frequently occurs on the Schuylkill. Records indicate that the Schuylkill at Pottstown floods every three years (based upon a 210-year period of record, Bourquard and Associates, p.
11-8, Ref 2.2-13). Flooding disrupts aquatic habitat and causes temporary degradation of water quality due to increased runoff from point and nonpoint pollution sources. The record flood at Pottstown occurred in June 1972 with the passage of Tropical Storm Agnes. At Pottstown, this flood crested at a river discharge of 2714 m3 /s (95,900 ft 3 /s). Flood waters that accompanied Agnes inundated nine large, used-oil storage lagoons at Douglassville, Pennsylvania, and flushed approximately 22,700 m3 (6x10' gal) of sludge into the river. This created the largest inland oil spill ever recorded. A similar spill from the same source had occurred in 1970 when 11.4 m3 (3012 gal) of oil sludge were flushed into the river. Acute effects of the spills were obvious, but chronic effects may be subtle, and still operating since oil has persisted in bottom sediments.
Heavy metals are an additional stress in the vicinity of LGS.
Schuylkill River sediments are particularly contaminated with 2.2-18
LGS EROL heavy metals (Reisinger, Ref 2.2-14), and serve as a constant source of contamination in the aquatic food chain. The metals have come from many sources, most of them anthropogenic. Coal mine water, with its low pH, provides a means by which naturally occurring metals such as copper, arsenic, and zinc are brought into solution. Effluents from metal processing industries and sewage treatment plants upstream of LGS also contribute to heavy metal contamination. Spills in the Douglassville area were a major source of heavy metal contamination since the sludge was the unreclaimable fraction of used crankcase oil.
Nutrient loading from point sources, such as sewage treatment plants, occurs near LGS and nitrogen, phosphorus, and carbon are present in elevated concentrations (Delaware Valley Regional Planning Commission and Chester-Betz Engineers, Ref 2.2-15; also see Section 2.4). Nutrients stimulate aquatic plant growth that may create nocturnal sags in dissolved oxygen (DO) concentration.
Aquatic plants also remove nutrients and toxicants from the sediments, and thus incorporate them into the food chain.
Nonpoint source runoff also is a stress. Much of the land upriver of LGS is developed, or used for agriculture. Runoff from such areas generally contains high silt and nutrient concentrations. Nutrients originate not only from farmland, but also from on-lot sewage treatment facilities. Pesticides are also present. These compounds may persist in the environment, and some are bioamplified as they pass through aquatic food chains. Polychlorinated biphenyls (PCB's) are present in runoff from landfill areas. The Pennsylvania Department of Environmental Resources' surveys (unpublished) indicate that fish upstream of LGS contain higher levels of PCB's than fish from any other part of the Commonwealth.
Dams installed for navigation purposes have been present on the Schuylkill since colonial times. The greatest number of dams present at one time was 38 in 1820 (Bourquard and Associates, Ref 2.2-13); today there are nine. The five dams between LGS and the Delaware River prevent migration of anadromous and catadromous fishes, and reduce habitat heterogeneity.
2.2.2.1.2 Phytoplankton Phytoplankton near LGS was studied in 1973 and 1974 (Tables 2.2-8 and 9). In all, 68 genera were identified, and diatoms were the most abundant (Table 2.2-10). Seasonal succession of major groups was typical of a temperate river and accompanied seasonal changes in water temperature. Diatoms were most dominant in spring, when they comprised up to 99% of total phytoplankton, and gradually decreased to 30 to 40% of the community in summer.
Navicula, Cyclotella, Nitzschia, Melosira, Syneda, and 2.2-19
LGS EROL Asterionella were dominant. Numbers of green algae were highest in summer (up to 50% of total), decreased with the onset of lower temperatures in late fall, and were lowest in winter and spring.
Scenedesmus and Ankistrodesmus were the most numerous green algae, and attained maximum densities in late August. Blue-green algae occurred in greatest numbers in the fall, but never comprised more than 2% of the total. The two most common blue-greens were Stichosiphon and Cylindrospermun. In general, phytoplankton density was low, characteristic of shallow lotic systems in temperate regions. They were not considered to have a major role in the trophic structure in this reach of the river.
2.2.2.1.3 Periphyton Periphyton is a seasonally important primary producer in the Schuylkill River, and may be impacted by plant discharge. The periphyton community near LGS was studied by the Applicant's consultant in 1973 and. 1974. (Tables 2.2-8 and 9).
2.2.2.1.3.1 Species Inventory In all, 26 genera of algae were observed on Plexiglas slides (Table 2.2-11). Algae in the periphyton community were largely diatoms (19 genera), although 5 genera of green algae, and 1 genus of blue-green algae also were present. Diatoms typically dominate periphyton in stony streams and rivers.
2.2.2.1.3.2 Community Description Seasonal changes in periphyton flora were observed. Genera typical of winter included Navicula, Diatoma, and Gomphonema. In spring, these diatoms declined in abundance, although Navicula remained dominant, and were joined by the diatoms Cymbella, Melosira, Cocconeis, and Synedra. Desmids, Closterium and Cosmarium, were often abundant in late spring and early summer.
In early autumn, there was a short recrudescence of growth as water temperature declined, and some spring diatom flora again became very common. With the onset of winter, the periphyton community declined as all but winter diatoms disappeared.
Periphyton populations built up during periods of low river velocity and turbidity were often scoured from the substrate during sudden increases in river discharge. For example, periphyton standing crop declined from a yearly maximum of 134 mg/dm2 on May 7, 1974 to 17 mg/dM2 on May 14, as a result of 2.2-20
LGS EROL substantially increased velocity over the 7-day period (Table 2.2-11). However, populations recolonized rapidly.
The annual pattern of periphyton growth in the Schuylkill River was typical of lotic systems in temperate regions. Periphyton productivity was highest in summer and fall, except for periods of high velocity. The highest estimated daily growth rate (10 mg organic matter/dm2/day) occurred during low flow in September 1974. Lowest productivity occurred in winter and early spring when river discharge was high (due to rain and meltwater), and temperatures were low.
2.2.2.1.3.3 Important Species Periphytic algae were considered important if, by qualitative microscopic observation, they appeared dominant at any time on plates selected randomly throughout the study. These taxa were considered critical to the existing structure and function of the ecosystem (Section 2.2). Eight diatom genera (Nitzschia, Navicula, Cocconeis, Synedra, Melosira, Diatoma, Cymbella, and Gomphonema) and two green algae genera (Cosmarium and Closterium) met this criterion (Table 2.2-11). Blue-green algae were not common at any time during the study.
2.2.2.1.4 Macrophytes Aquatic macrophytes are seasonally abundant primary producers in the Schuylkill near LGS, and were studied in 1984 and 1977 (Tables 2.2-8 and 9). Macrophytes downstream of LGS may be affected by plant discharge.
2.2.2.1.4.1 Species Inventory In all, 10 species of aquatic macrophytes, representing 3 divisions and 9 families, were found in the vicinity of LGS (Table 2.2-12). Eight species were aquatic angiosperms, one a filamentous green alga (Cladophora sp.), and one a moss (Fissidens sp.). All are submergent except Lemna minor (floating), Jussiaea repens (emergent with an extensive mat of floating leaves), and Sagittaria latifolia (emergent). Lemna minor, usually uncommon in lotic systems, was abundant in the river during low flow periods. Elodea canadensis was common in 1974, but was rare in 1977.
2.2-21
LGS EROL 2.2.2.1.4.2 Community Description Peak growth of macrophytes in 1977 occurred in mid-July, when they (exclusive of Cladophora) occupied 20 to 25% of the river's surface area (Figure 2.2-4). The plant community was loosely structured with no persistent species associations. Growth patterns were influenced by current; generally, each plant species formed hummocks that were separated by channels of swift water.
Species composition in various areas did not change appreciably during the 1977 growing season (May-September). Generally, plants present in an area simply became more abundant.
Occasionally, a species (e.g., P. crispus) invaded new areas.
Rarely was a species observed to disappear from an area where it had become established. This did occur near S75700, however, where M. exalbesecens was present in spring, but reduced or absent in midsummer; by late summer it had reappeared.
Throughout the growing season, a multifarious group of organisms used the macrophyte beds. Macrophytes provided habitat for numerous macroinvertebrates, particularly Ephemeroptera, Trichoptera, and Chironomidae. The snails Goniobasis virQinica and Physa were observed grazing on macrophytes in high numbers in August. The plants also provided cover for many fish.
Macrophytes were used as substrate by epiphytic algae, and the quiet water created by extensive beds supported large quantities of the filamentous green algae Spirogyra and Hydrodiction.
Autochthonous detritus was added to the river during dieback in the fall.
2.2.2.1.4.3 Important Species Important species were selected by criteria described in Section 2.2, and on the basis of relative qualitative abundance (Section 6.1.1.2.2.3). Abundant or common species (Table 2.2-12) were considered important and included Cladophora sp., Potamogeton crispus, P. berchtoldi, Heteranthera dubia, and Myriophyllum exalbescens. All are submergent. Important species occurred throughout the study area; some locations contained a heterogenous mixture of plants, whereas other areas were dominated by a single species. Pertinent local data on important species are provided below.
2.2.2.1.4.3.1 Thallophyta Cladophora, an attached alga, was ubiquitous in the river near LGS and generally absent only from areas of low current (e.g.,
2.2-22
LGS EROL backwater areas and in the lee of large hummocks of other macrophytes). It generally exhibited a bimodal growth curve.
Growth was relatively extensive in May, reduced in July, and extensive again in late August.
2.2.2.1.4.3.2 Spermatophyta The remaining important species (Potamogeton crispus, P.
berchtoldi, Heteranthera dubia, Myriophyllum exalbescens) are vascular plants. They are rooted in the substrate and possess adventitious roots that enable them to maintain their position in the current. Growth began in April or May and continued until September or October. In the fall, plants either died back to persistent roots or stolons (e.g., P. crispus), or stopped growing (e.g., M. exalbescens).
2.2.2.1.5 Zooplankton Zooplankton near LGS was not studied, but results of a study conducted 13 km downriver in 1975 and 1976 provided information on composition, density, and seasonality (PECo: p.3-13, Ref 2.2-16). The mainstream zooplankton community was dominated by rotifers, copepods, and cladocerans. Mean seasonal density was highest in spring (22,784/M 3 ) and fall (22,334/M 3 ), and lowest in summer (4649/m 3 ) and winter (6524/M3). These densities are relatively low, and typical of middle reaches of moderately sized rivers. Zooplankton in this section of the Schuylkill was not considered to have a dominant role in the trophic structure, and likely does not at the Limerick site.
2.2.2.1.6 Macroinvertebrates The macroinvertebrate community in the Schuylkill River near LGS plays an important functional role by converting allochthonous and autochthonous materials into temporary storage within their own tissue, ultimately becoming an essential component in the food web. Macroinvertebrates also shred coarse organic material (e.g., leaves) into finer particles that can be utilized by smaller macroinvertebrates. Plant operation is expected to affect Schuylkill macroinvertebrates through entrainment of drift, and water quality changes caused by blowdown discharge.
Macroinvertebrates were studied from 1970 through 1976 (Tables 2.2-8 and 9).
2.2-23
LGS EROL 2.2.2.1.6.1 Species Inventory Macroinvertebrates collected by all methods and from all habitats from 1970 through 1976 represented 8 phyla, 30 orders, 81 families, 218 genera, and at least 297 species (Table 2.2-13).
The taxonomic distribution included all major orders of aquatic insects, 6 orders of annelids, 4 orders of molluscs, and 3 orders of crustaceans. The greatest taxonomic diversity (number of taxa) was found in the orders Diptera and Ephemeroptera that contained representatives of 16 families and at least 108 species, and 6 families and at least 55 species, respectively.
Trichoptera, Odonata, Plecoptera, and Plesiopora also showed considerable diversity. Of the remaining 24 orders, 13 were represented by only one or two species. The most diverse family was Chironomidae, represented by 37 genera.
The kinds and number of macroinvertebrate species found in the river near LGS agreed well with previous surveys of the Schuylkill (Wurtz and Dolan, Ref 2.2-46), and other eastern temperate rivers (Patrick, Ref 2.2-47). The highest number of insect taxa reported by Patrick (Ref 2.2-47) for any of the 9 rivers she studied was 95 in the upper Potomac. The number of taxa reported by Wurtz and Dolan (Ref 2.2-46) was 160 for the Schuylkill River about 10 km downriver from LGS. The relatively high diversity recorded by the Applicant's consultant resulted from the long (6-year) study, which provided considerably more seasonal data.
A relative qualitative abundance was assigned to each taxon on the species list based upon the following: abundant - organisms found in almost all samples, and usually present in relatively high numbers; common - organisms found in over one-half of all samples, but usually present in relatively low numbers; uncommon - organisms found only occasionally in samples (i.e.,
several times a year), and present in low numbers; and rare -
organisms found in one sample per year or once every few years and present in very low numbers. Bias was inherent in these subjective abundance terms since the majority of samples were collected with cylinder samplers in run/rubble habitat. For example, organisms listed as rare or uncommon in run habitat (dominant near LGS) may have been common or abundant in backwater or littoral areas.
2.2.2.1.6.2 Community Description Annual mean densities (no./m 2 ) were consistently higher at the upstream station than at downstream stations (Table 2.2-14).
This was due mainly to the higher number of midge larvae upstream. Annual mean densities (g dry wt/m 2 ) have increased by 2.2-24
LGS EROL station in an upstream progression since 1972 (Table 2.2-15). As noted below, this increase was due almost entirely to the upstream movement of the river snail Goniobasis virQinica.
The monthly total of taxa per sample did not differ significantly from 1974 to 1976 at any station (Table 2.2-18). The total number of taxa was reduced in 1973 because the macroinvertebrate community was still recovering from the June 1972 flood and oil spill (Section 2.2.2.1.1).
Only five taxa (Tubificidae - predominantly Limnodrilus hoffmeisteri, Chironomidae - predominantly Cricotopus bicinctus, Goniobasis virginica, Physa heterostropha, Cheumatopsyche spp.)
comprised over 10% of the total number in any year (Table 2.2-14). Tubificids were abundant at S76760 and 575770, and comprised up to 64% of the total number of organisms collected at S76760 in 1973. Chironomids were abundant at S78620, and reached their maximum relative abundance (54%) at this station in 1973. P. heterostropha was dominant in 1972 at S78620, where it comprised 68% of all organisms collected. This was the only time this snail was relatively dominant in any year, or at any station. The reason for this is unknown, but may have been due to a selective advantage gained from the 1972 flood. G.
virginica was not relatively abundant until 1974 at the two downstream stations. It comprised up to 53% of the total number of organisms collected in 1974 at S76760. It has increased in relative abundance upstream since 1974. Cheumatopsyche spp. have recovered from the 1972 flood and oil spill to the point where, at*S78620, it was second only to Chironomidae in relative abundance in 1976.
Before the fall of 1973, the snails Helisoma anceps and P.
heterostropha, tubificids, and occasional crayfish and leeches dominated biomass in most samples. Although some organisms such as midges were relatively abundant by number, they made up only a relatively small percentage of total biomass due to their small size. Since the fall of 1973, G. virginica has comprised over 90% of the total biomass in many samples, especially at downstream stations.
2.2.2.1.6.3 Important Species NRC criteria for selection of important species (Section 2.2) are quite broad in scope. Many macroinvertebrate species could be considered important in terms of either being a food source for recreationally valuable species (fish), or a critical link in the structure and function of the aquatic ecosystem. To limit the number selected, taxa considered critical to the community were restricted to those that comprised 2% or greater of the total number or biomass in any annual collection at any station, or 2.2-25
LGS EROL macropredators that occurred frequently in monthly quantitative samples.
On this basis, 17 taxa were selected: Dugesia tiorina, Prostoma graecense, Tubificidae, Crangonyx aracilis, Cheumatopsyche spp.,
Hydropsyche phalerata, Chironomidae, Physa heterostropha, Helisoma anceps, Ferrissia tarda, Goniobasis virQinica, Pisidium spp., Sphaerium spp., Erpobdella punctata, Cambarus bartoni, Orconectes spp., and Arcia spp. The last four taxa are macropredators. Most of these taxa were highly dominant in the river in all years and at all stations. Together, they comprised over 90% of the total number collected in every year and at all stations.
The following treatment of important species includes information on taxonomy, local distribution, life cycle, and food habits.
Population dynamics are also discussed and include data on spatial and temporal variation in numbers (Table 2.2-16), and biomass (Table 2.2-17). These tables complement the text description.
2.2.2.1.6.3.1 Dugesia tigrina This planarian was collected at all stations in similar numbers.
The highest annual mean density (387/m 2 ) occurred in 1972 at 575770. In 1973, densities declined at all stations and remained below 1972 levels through 1976. Peak seasonal density usually occurred in late summer and fall, and maximum density in a single sample (1836/m 2 ) was recorded in October 1972 at 575770.
Variability in biomass density (1972-1974) was similar to that for numbers.
2.2.2.1.6.3.2 Prostoma graecense This nemertean was collected at all stations. Highest annual mean density (521/M 2 ) occurred in 1972 at S75770. In 1973, densities declined at all stations, and by 1976 had not regained 1972 levels, except at 578620 in 1975. Peak seasonal density occurred in late summer or fall, and worms were rarely collected the rest of the year. Maximum density in a single sample (2123/m 2 ) was recorded in November 1972 at S75770. Variability in biomass density followed the same trend as variability in numerical density.
2.2.2.1.6.3.3 Tubificidae Aquatic oligochaetes were identified only to family. Large numbers of tubificids were collected from the river, and the considerable time required to clear, mount, and identify all 2.2-26
LGS EROL specimens was prohibitive. However, in qualitative samples (1972 and 1973), and subsamples of quantitative samples (1976),
tubificids were identified to species to determine the species present and their relative abundance. These samples revealed that Limnodrilus hoffmeisteri was by far the most abundant tubificid in the Schuylkill River study area, and that the only other tubificid present in relatively high numbers was Peloscolex multisetosus.
Tubificids are preyed upon by many aquatic invertebrates, and by fishes. In the river, two cases of predation on tubificids were recorded: (1) the leech Erpobdella punctata preyed heavily on tubificids and (2) chironomids (mainly Pentaneourini) cleared for identification showed considerable quantities of tubificid setae and whole parts in their guts.
Highest annual mean density (3972/M 2 ) of tubificids in the river occurred in 1972 at S75770. Densities at S76760 and S75770 were consistently higher than at S78620 in all years. Substrate at S78620 was not ideal for tubificids, and a greater number of predatory chironomid larvae and leeches were present. Peak seasonal density at all stations usually occurred in spring or summer, but fairly large numbers were present throughout the year. Maximum density in a single sample (14,898/M 2 ) was recorded in June 1973 at S76760. Maximum biomass density in a single sample (4.5 g dry wt/m 2 ) occurred in July 1972 at S75770.
Variability in biomass closely followed variability in numbers.
2.2.2.1.6.3.4 Erpobdella punctata This leech was collected at all stations, but the highest densities were found at S78620. Highest annual mean density (20/M 2 ) occurred in 1975 at S76760. Peak seasonal density 2
usually occurred in spring and summer. Maximum density (135/M )
was recorded in June 1974 at S78620. Maximum biomass density (0.9 g dry wt/M 2 ) occurred in September 1973 at 578620.
In 1973, a study of food habits was conducted to determine the kinds of food consumed by E. punctata. It was found that, on an annual basis, food consisted of about 50% tubificids and 50%
chironomids. Cricotopus and PolVpedilum were the most frequently ingested midge larvae. The unusual abundance of predatory leeches (particularly Erpobdella) in the river was probably responsible for the relatively small number of tubificids present at any one time at S78620. E. punctata was occasionally consumed by fish in the study area.
2.2-27
LGS EROL W 2.2.2.1.6.3.5 Crangonyx gracilis This amphipod was found at all stations in the river. Highest annual mean density (432/M 2 ) occurred in 1976 at S75770. Annual mean density of C. gracilis has increased steadily at all stations since 1972. Peak seasonal density averaged highest in the spring, but densities were also relatively high in summer and fall. Maximum density in a single sample (2275/M 2 ) was recorded in June 1976 at S75770. Variability in biomass density followed the same trend as that for numbers.
2.2.2.1.6.3.6 Crayfish The three crayfish species found in the Schuylkill study area, Orconectes obscurus, 0. limosus, and Cambarus bartoni, are well described and easily differentiated on the basis of mature males (Hobbs, Ref 2.2-48). However, unidentifiable females and immature males of Orconectes were frequently collected so the two species were treated at the genus level. All species were found at all sample stations, but were more common at downstream stations (576760 and S75770).
e Highest annual mean density (1/m 2 ) of C. bartoni occurred in 1976 at S78620. Peak seasonal density usually occurred in the fall.
Maximum density in a sample (8/M 2 ) was recorded in December 1974 at S75770, and in April 1976 at S78620. Maximum biomass density in a single sample (3.3 g dry wt/m2) was recorded in October 1972 at S76760.
Highest annual mean density (2/M 2 ) of Orconectes spp occurred in 1976 at S78620. Peak seasonal density usually occurred in late spring and early summer. Maximum density in a sample (20/M 2 ) was recorded in June 1975 at S76760, and in September 1975 at S76820.
Maximum biomass density in a single sample (13.9 g dry wt/m 2 ) was recorded in December 1974 at S75770. Although numerical densities for both taxa were quite low, crayfish comprised a relatively high percentage of biomass.
It is known from food habits studies that various fish and probably turtles, and birds, racoons, muskrats, and snakes in the river consume crayfish. Mature crayfish stay in burrows or under rocks during the day, and come out to feed at night. Immatures are active at any time.
2.2.2.1.6.3.7 Argia spp.
Damselfly naiads were collected at all stations in the study area. Highest annual mean density (85/M 2 ) was recorded in 1976 at 575770. Annual mean densities have increased since 1974.
Peak seasonal densities usually occurred in late summer and fall.
2.2-28
LGS EROL Maximum density in a single sample (459/M 2 ) was recorded in September 1975 at S76760. Maximum biomass density in a single sample (0.2 g dry wt/M 2 ) occurred in November 1973 at S76760.
Atria spp. adults were observed emerging in June, and flight activity was observed throughout summer. The immatures are found on and under the surface of large and small rocks, and are voracious predators.
2.2.3.1.6.3.8 Cheumatopsyche spp.
Whereas most adult species of Cheumatopsyche have been described, the larval stages have not been associated and thus larvae were treated at genus level. Cheumatopsyche spp. were commonly collected at all stations. Highest annual mean density (2413/M 2 )
was recorded in 1976 at S78620. Highest densities were always recorded at station S78620, where faster current velocity was probably conducive to more efficient net feeding.
Peak seasonal densities occurred in summer. Maximum density of Cheumatopsyche spp. in a single sample (7299/M 2 ) occurred in September 1976 at S78620. A marked increase in density has occurred since 1972. This increase probably reflects recovery from the flood and oil spill of 1972 (Section 2.2.2.1.1).
Variability in biomass paralleled changes in numerical density.
2.2.2.1.6.3.9 Hydropsyche phalerata This net-building caddisfly was collected at all stations in the river. Highest annual average density (838/M 2 ) occurred in 1975 at S78620. Peak seasonal density occurred in the summer, and maximum density in a single sample (3533/M 2 ) was recorded in September 1975 at S78620., Like Cheumatopsyche spp., H. phalerata has increased markedly in density since 1972. Variability in biomass paralleled changes in numerical density.
2.2.2.1.6.3.10 Chironomidae Due to the relatively large number of midge larvae collected in quantitative samples and the time required to clear, mount, and identify them, midges were identified to genus or species only in 1974 and 1976. Dominant chironomid taxa were Cricotopus bicinctus (most abundant),-other unidentifiable species of Cricotopus, Polypedilum spp., and Pentaneurini. For quantitative data analysis, midges were treated at the family level.
2 Highest annual mean density of chironomidae larvae (5288/M )
occurred in 1974 at S78620. No pattern in density was apparent between years or stations. Peak seasonal densities usually 2.2-29
LGS EROL occurred in the spring. Maximum density in a single sample (20,889/M 2 ) was recorded in March 1974 at S78620.
2.2.2.1.6.3.11 Physa heterostropha This pulmonate snail was found at all stations. Highest annual mean density (10,038/M 2 ) occurred in 1972 at S78620. Peak seasonal density always occurred in the fall. Maximum density in a single sample (30,635/m 2 ) was recorded in November 1972 at S78620, and the biomass of this sample (24.4 g dry wt/m 2 ) was also the highest recorded. Densities declined after 1972 and this may have been due to replacement by Goniobasis virginica, another dominant snail in the river.
2.2.2.1.6.3.12 Helisoma ances This snail was collected at all stations. Highest annual mean density (654/M 2 ) occurred in 1974 at S78620. Peak seasonal densities usually occurred in the summer. Maximum density in a single sample (4365/m 2 ) was recorded in August 1974 at S78620.
Wherever G. virginica moved in, H. anceps seemed to be replaced.
This may be related to competition for food or space.
2.2.2.1.6.3.13 Ferrissia tarda This limpet was collected at all stations. Highest annual mean density (515/M 2 ) occurred in 1972 at S78620. Peak seasonal density usually occurred in the fall. Maximum density in a single sample (1860/M 2 ) was recorded in October 1972 at S76760.
2.2.2.1.6.3.14 Goniobasis virainica Highest annual mean density (4325/M 2 ) of G. virginica occurred in 1975 at S76760. Peak seasonal density occurred in summer and fall. Maximum density in a single sample (18,984/m 2 ) was recorded in November 1974 at S76760. From 1970 to 1972 this snail was collected only from the downriver station, but from 1973 through 1976 the population moved steadily upriver. For example, the annual mean number of G. virQinica collected from or near the farthest upstream station (S78620) in successive years was zero in 1970 and 1971, 3/M2 in 1972, 16/M 2 in 1973, 1159/M 2 in 1974, 2096/M 2 in 1975, and 2221/m 2 in 1976. Since mid-1973, the biomass of almost every sample has been highly dominated by this snail. Maximum biomass (185 g dry wt/m 2 ) occurred in November 1974 at S76760.
2.2-30
LGS EROL This snail appeared to be most abundant in run habitat where current was moderate (near 0.3 m/s). Snails oriented themselves with their spires pointed downstream. Snails observed in slackwater areas and near banks were not positioned in any particular manner. Crutchfield (Ref 2.2-49) reported a positive rheotaxis for closely related G. proxima in Bolin Creek, North Carolina, where 53 marked individuals all moved upstream over a 15-week period. It is therefore possible that the upriver movement of this local population may represent a normal phenomenon.
2.2.2.1.6.3.15 Pisidium spp.
Highest annual mean density (621/M 2 ) of these fingernail clams occurred in 1976 at S78620. Since 1972, densities have generally increased in most years and at all stations. Peak seasonal densities occurred in the fall, and the maximum density in a single sample (2218/M 2 ) was recorded in November 1976 at S78620.
Maximum biomass density in a single sample (0.1 g dry wt/m 2 ) was recorded in January 1973 at S78620.
2.2.2.1.6.3.16 Sphaerium spp.
Highest annual mean density (1130/mz) of these fingernail clams occurred in 1972 at S78620. Peak seasonal densities occurred in the fall. Maximum density in a single sample (4357/M 2 ) was recorded in November 1972 at S78620, and maximum biomass density (5.2 g dry wt/m 2 ) was recorded in December 1972 at S78620.
2.2.2.1.6.4 Drift For many benthic macroinvertebrates, drift is apparently a passive phenomenon that occurs when organisms are dislodged by the water current and enter the water column. Drifting macroinvertebrates are utilized as a food source by many fish predators. Macroinvertebrate drift was studied from 1972 through 1975. (Tables 2.2-8 and 9).
The only important benthic taxa abundant in drift were Chironomidae, Cheumatopsyche spp., and Hydropsyche phalerata.
The remaining important taxa (mostly worms, leeches, crayfish, and snails) were found only rarely in drift samples, due either to their weight (e.g., crayfish, snails), ability to swim against the current (e.g., the leech Erpobdella punctata), or burrowing ability (e.g., Tubificidae). Taxa that were common in drift but rare or uncommon in benthos samples were the mayfly Tricorythodes sp., and the moth-flies Psychoda spp. and Telmatoscopus albipunctatus. These organisms were rarely collected in benthic 2.2-31
LGS EROL W samples because their preferred habitat was not run/rubble (where benthic samples were collected).
In all, 8 drift taxa were highly dominant and together comprised over 95% of all organisms collected each year (Table 2.2-19).
Chironomidae (larvae and pupae) averaged almost 50% of all drift organisms collected in all years. Since chironomids were identified only to family level in most years, intrafamily changes were not determined. However, chironomids dominant in benthos (Cricotopus spp. and Polypedilum spp.) were also dominant in drift. The next most abundant taxa were psychodid pupae (Psychoda sp., Telmatoscopus albipunctatus) and Tricorythodes sp.
Variability of monthly drift densities (no./1000 M3 ) within any year was quite high (Table 2.2-20) and most likely caused by the variability and short duration of chironomid pupation and emergence. No significant difference in monthly drift densities among years (1972-1974) was observed.
Because most benthic macroinvertebrates in the river were nocturnal feeders, increased levels of drift densities and taxa usually occurred during hours of darkness. This relationship between drift and changes in light intensity has been well-
- documented (Waters, Ref 2.2-50). However, only in summer did chironomids drift in greater densities at night, the rest of the year they showed no definite periodicity.
Drift densities (no./m 3 ) were compared with benthos densities (no./m 2 ) using Elliott's (Ref 2.2-51) method (see Section 5.1.3.2.2a). The percentage of benthic organisms present in the drift at any given time was found to be quite low, and ranged from 0.0002 to 1.3140% (Table 2.2-21).
2.2.2.1.7 Fish Fish in the Schuylkill River are gradually recovering from an extended period of environmental degradation (Section 2.2.2.1.1).
The river presently supports fish fauna typical of large warmwater rivers of the mid-Atlantic area of North America. The community contains many species and is dominated by cyprinid, centrarchid, and ictalurid fishes. Several species are actively sought by recreational fishermen (Harmon, Ref 2.2-52). It is anticipated that completion of fish passage facilities at the remaining river dams will restore anadromous fish runs.
Operation of LGS may affect the existing fish community through water withdrawal (i.e. entrainment-impingement) and blowdown
- discharge. To evaluate these potential impacts, the fish 2.2-32
LGS EROL community has been intensively studied for several years by using several types of gear (Tables 2.2-8 and 9).
2.2.2.1.7.1 Species Inventory Fishes representing 42 species of 10 families, as well as hybrids within Cyprinidae, Esocidae, and Centrarchidae have been collected from the Schuylkill River and its tributaries near LGS since 1970 (Table 2.2-22). Of these, 27 were native to the drainage and 15 were introduced. None is considered threatened or endangered by either Federal or State regulatory agencies.
Determination of qualitative abundance was made by subjective comparison of catch statistics as follows: abundant - fish that occurred regularly in large numbers (in samples taken with appropriate gear); common - those regularly collected in small numbers; uncommon - those irregularly collected in small numbers; and rare - those for which only a few individuals were collected throughout the study.
2.2.2.1.7.2 Community Description 2.2.2.1.7.2.1 Larval Fishes Most fishes in the Schuylkill River are lithophilous (i.e., eggs are deposited on rock or gravel bottom and prolarvae develop on this substrate) or phytophilous (egg and prolarval development take place on or among aquatic vegetation, above muddy or silted bottoms). Suitable spawning sites in the river are restricted primarily to shallow riffle sections and quiet areas near shore where current, cover, and vegetation are appropriate for egg deposition.
Larvae of fishes near LGS were sampled in the water column by drift nets and in shoreline nursery areas by trap and push net (Section 6.1). Most spawning occurred from May through August.
Larval fish drift density was low in April, peaked in June and late July or early August, and gradually declined through August (Figure 2.2-5). In nursery areas, larval fish were most abundant in early June, late July, and early August (Figure 2.2-6).
Unidentified minnows comprised the most abundant taxon in 1974 and 1975 drift collections, and accounted for 48 and 78% of the total catch, respectively (Table 2.2-23). In 1974, goldfish and carp were second and third in abundance. In 1975, white sucker and tessellated darter were the second and third most abundant taxa. Goldfish were the most abundant taxon (63%) in 1976, followed by minnows (25%) and Carp (7%). Larvae of Micropterus 2.2-33
LGS EROL sp. and brown bullhead rarely occurred in drift, probably because of the parental care adults afford their young. Most bullhead collected were recently transformed juveniles. Mean daily drift density in the east channel for the 1974, 1975 and 1976 major spawning periods (May-August) was 0.45, 0.09, and 0.59 fish/m*,
respectively. Densities were greatest between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br />, and usually peaked at 2200, 2400, or 0400 hours0.00463 days <br />0.111 hours <br />6.613757e-4 weeks <br />1.522e-4 months <br />.
Drift densities in these hours ranged from 3 to 95 times greater than daytime densities. Total biomass of drifting larvae usually varied with fluctuations in numeric density.
Vertical distribution of ichthyoplankton in the water column frequently varies (Taber, Ref 2.2-54 and Marcy, Ref 2.2-55). In the Schuylkill River, drift density was significantly greater near the bottom in the day. Density at night was greater near the surface but differences in catch with depth usually were not significant.
A definite horizontal gradient in larval fish drift was observed in the river (Table 2.2-24). Numeric density, as measured at different locations across the east channel around Limerick Island, was significantly different at night in 1974 with greatest larval abundance occurring.near the Montgomery County shore. Biomass showed a similar pattern. In 1975 and 1976, density across the entire river was significantly different at night and during 24-hour periods. Densities generally decreased with increasing distance from shore.
The relative abundance of shoreline larvae sampled by trap was dissimilar to that of drifting larvae during the 1975 spawning period. Unidentified minnows, goldfish, and carp were the major components of trap-net catch (Table 2*2-25).
In push-net collections Lepomis spp. and unidentified minnows were the most widely distributed taxa; in 1976 each was collected from 11 of the 13 stations (Table 2.2-26). Goldfish, unidentified minnows, and Lepomis spp. were the most abundant taxa (all stations combined). White sucker and tessellated darter were infrequently collected, probably because their early developmental period was nearly completed at the time of sampling. Use of nursery areas depended upon habitat and time of spawning of each species. Some sites had habitat suitable to a variety of species and were occupied throughout the spawning season (S77320 and S77161), while other sites with limited desirability were used only occasionally (S77485, intake location). Most (70%) larvae were collected from S77161, S76794, S76970, and S77320 while greatest diversity (6 taxa) occurred at S77970 (Table 2.2-26). Catch-per-unit-effort of larvae was generally greater downstream of LGS and along the west shore (Table 2.2-27).
2.2-34
LGS EROL 2.2.2.1.7.2.2 Minnows and Young Adult minnows and young of other species were sampled by seine and DC electrofishing in conjunction with small fish population estimates (Section 6.1). Seine collections made in 1975 and 1976 revealed 8 families and 35 species (Table 2.2-28). In both years, swallowtail shiner 'and spotfin shiner dominated the catch, accounting for 95 and 88% of the total catch in 1975 and 1976, respectively. Relative abundance of the 15 most abundant species common to both years showed no significant relationship between years. A decrease in dominance of swallowtail shiner and spotfin shiner in 1976, and a concomitant increase in numbers of other species was responsible for the lack of association between years. Because these 2 species so completely dominated minnow populations, any change in their abundance affected total population structure.
The majority (92%) of fish collected in 1975 were captured from January through May at stations S81750, S77960,,S76820, and S75730 (Tables 2.2-29 and 30). These sites were probably typical of important overwintering areas. A small increase in abundance occurred in September as a result of recruitment of young. In 1976, major peaks in abundance occurred from June through December and indicated that a more successful spawn occurred in this year. Large catches (>1000) were made at S77240, S77220, and S76820, which emphasized the importance of these areas as spawning and nursery habitat.
The diversity, or total number of species collected (Tables 2.2-29 and 30) peaked in 1975 during periods of winter aggregation, and after late spawns in September. In 1976, peaks occurred after spawns and in a mid-winter aggregation period.
The number of species collected varied between stations (Figure 2.2-7). Peaks in both years occurred in areas of dense aquatic plants, or areas of spawning or nursery activity.
Relative abundance determined from electrofishing catches generally agreed with seine information, except for sunfish that were more abundant in electrofishing catches (Table 2.2-31).
This was probably due to the cover-seeking behavior of small sunfish, which made them less susceptible to capture by seine, and the fact that sunfish were actively pursued in electrofishing.
2.2.2.1.7.2.3 Adults Three programs were employed to sample adult fishes; the large fish population estimate, catch-per-unit-effort programs, and the Vincent Pool trap-net program (Section 6.1). Population estimate 2.2-35
LGS EROL and catch-per-unit-effort sampling was conducted throughout the study area; trap-net sampling was conducted only in Vincent Pool.
In three years of population estimate sampling, pike and sunfish hybrids and 21 species representing 6 families were collected (Table 2.2-32). In all sites and all years the catch was dominated by brown bullhead, redbreast sunfish, pumpkinseed, white sucker, and goldfish. The catch of these five species combined represented a minimum of 85% (S76440, Limerick B, 1975) and a maximum of 94% (S77240, Limerick A, 1974) of total catch.
Brown bullhead was the most abundant species on four occasions (Limerick A, 1974 and 1975; Limerick B, 1974 and 1975), redbreast sunfish on two occasions (Limerick B, 1973; S79440, Firestone, 1974), and pumpkinseed on two occasions (Limerick B, 1973; S74365, Vincent Pool, 1974).
Although there were changes in species ordering, species composition in the study area was consistent over the study period. Species composition upstream (Firestone) was similar to that of the intake site (Limerick A), the discharge site (Limerick B), and the recovery site (Vincent Pool).
The limited data presently available from the catch-per-unit-effort program describe a similar fish community (Table 2.2-33).
In all sites except Vincent B the catch was dominated by brown bullhead, redbreast sunfish, pumpkinseed, white sucker, and goldfish. These five species ranged from 33% of the catch at Vincent B to 88% at Firestone. Lower abundance at Vincent B was due to large winter catches of golden shiner, which made up 52%
of total catch at that site. Species relative abundance was significantly correlated among all sites.
In trap-net collections at Vincent Pool, 27 species representing 7 families, as well as Lepomis and minnow hybrids, were taken from May 1971 through December 1976 (Table 2.2-34). The most abundant species were pumpkinseed (44% of total), brown bullhead (30%), redbreast sunfish (5%), green sunfish (3%), and white crappie (3%). Species composition at Vincent Pool, determined from trap-net collections, was similar to that determined from the population estimate and catch-per-unit-effort sampling in the same area. The brown bullhead was more abundant in trap-net catches, probably due to trap-net selectivity for demersal species.
2.2.2.1.7.3 Important Species General criteria for selection of important species were given in Section 2.2. Schuylkill fishes selected as important represented all major ecological niches available, as well as taxa of sociological importance. All will be potentially affected by 2.2-36
LGS EROL plant operation. A list of important fishes with more specific justification is given in Table 2.2-35. A relatively large number of species were selected because the plant will have diverse impacts (entrainment, impingement, discharge) and the adjacent Schuylkill supports a recreational fishery. The local biology of important species is described below.
2.2.2.1.7.3.1 American Eel The American eel (Anguilla rostrata) was common in the river and comprised 2% of the large fish taken in 1976 catch-per-unit-effort sampling (Table 2.2-33). Monthly catches exhibited significant variation, with the July catch significantly greater than December's (Table 2.2-36). The catch did not. vary significantly among sites. The American eel was commonly caught by recreational anglers and was the preferred species of a small number of fishermen (Harmon, Ref 2.2-52).
2.2.2.1.7.3.2 American Shad This specie (Alosa sapidissima) has not used the upper Schuylkill for spawning since the construction of the Fairmount Dam in Philadelphia in 1800-01 (Gay, Ref 2.2-56). Prior to this date, the Schuylkill River was an important shad fishing center. In 1784, 4000 shad were caught in a single net near Pottstown.
Lampreys, striped bass, and shad migrated as far upstream as Port Carbon (Nolan, Ref 2.2-57).
Sampling below the Fairmount Dam in 1975-1976 revealed that adults were present but uncommon (Philadelphia Electric Company, pp. 3-33, Ref 2.2-58). A shad restoration feasibility study conducted by the Pennsylvania Fish Commission (Marshall, Ref 2.2-59) indicated that there were sufficient numbers of shad present below the Fairmount Dam so that, given access to the upper river, a spawning population might be reestablished without extensive help from man. As a result of this study, fish passage facilities have been completed at Fairmount Dam and are proposed for the Flat Rock, Plymouth, Electric, Black Rock, and Vincent dams. Completion of the construction projects will provide shad with access to the river as far upstream as the Felix Dam at Reading (river km 127).
2.2.2.1.7.3.3 Muskellunge This species (Esox masquinongy) and its sterile hybrid with the Northern pike (Esox lucius) were rare in the Schuylkill River although both were stocked regularly by the Pennsylvania Fish Commission. No larval muskellunge were collected in drift or push-net sampling. Because no evidence of natural reproduction 2.2-37
LGS EROL
-- in the river was found, it is likely the population has been maintained entirely by stocking. Most recent stockings have been the Northern pike/muskellunge hybrid. Juveniles were rarely collected from the river; only one was collected in population estimate sampling (1973-1976) and seine sampling (1976).
However, several were collected by electrofishing in 1977. No adults equal to or exceeding the angling legal size limit were collected; the largest specimen was 463 mm FL.
2.2.2.1.7.3.4 Goldfish The reproductive period of goldfish (Carassius auratus) in the Schuylkill generally lasted from June through September at water temperatures of 21 to 270 C. Drifting larvae occurred throughout the summer in 1974, 1975 and 1976. Eggs from the river hatched in 54 hours6.25e-4 days <br />0.015 hours <br />8.928571e-5 weeks <br />2.0547e-5 months <br /> at 22.20 C.
Goldfish larvae were the second most abundant species in drift samples 1974, eighth in abundance in 1975 and first in abundance in 1976. Mean density in 1974, 1975 and 1976 was 0.1361/m3 (30%
of total), and 0.0002/m' (<1%), and 0.3753/mn (63%)
(Table 2.2-23). Peak densities in both years occurred between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br /> and densities were greater near shore than in
- midriver in 1975 and 1976 (Table 2.2-24). They were also greater in the west, rather than the east, channel around Limerick Island in 1975 and greater in the east channel in 1976.
Relative abundance of shoreline goldfish larvae adjacent to drift sites was dissimilar to that of drifting larvae in 1975.
Goldfish ranked second in abundance in trap collections and comprised nearly 37% of total catch (Table 2.2-25). Push-net sampling indicated that goldfish were the most abundant shoreline larvae in 1976 (Table 2.2-26). Larvae were generally more abundant along the west shoreline and downstream of the proposed LGS discharge (Table 2.2-27).
Young goldfish were rarely collected by seine, and only 15 specimens were captured in 1975 and 1976 combined (Table 2.2-28).
Only 14 were collected in connection with small fish population estimates conducted in 1973, 1975, and 1976 (Table 2.2-31).
Adult goldfish population size at Limerick sites A and B fluctuated from 1973 to 1977. A mean standing crop of 326 fish/ha was estimated in 1973, 140 fish/ha in 1975, and 378 fish/ha in 1977 (Table 2.2-37). No difference in population size was detected between Limerick A and B in 1975, the only year valid among-site comparisons could be made. The standing crop at Firestone was more consistent; estimates were 195 fish/ha in 1974 S and 259 fish/ha in 1977. The standing crop at Vincent Pool was estimated (1977)as 167 fish/ha.
2.2-38
LGS EROL In the second half of 1976, the goldfish catch-per-unit-effort did not show significant monthly variation. The catch-per-unit-effort did vary among sites, with catches at Limerick A significantly greater than those at Firestone and Vincent B (Table 2.2-36).
Estimates of the goldfish biomass standing crop at Limerick A and B generally varied in the same manner as numbers (Table 2.2-37),
and ranged from 31.6 kg/ha in 1975 to 74 kg/ha in 1977. The biomass standing crop was greater at Firestone than at Vincent Pool.
No fish older than age II were collected from the river and maximum length was only 250 mm. Most growth occurred in the first year of life (Table 2.2-38). The longest goldfish collected (all studies) was 320 mm FL. Goldfish length-weight relationships determined for Limerick A and B in 1975 are shown in Table 2.2-39.
Goldfish collected from the Schuylkill River were found to be subject to a number of maladies. Approximately 43% of individuals collected exhibited some symptom of disease or parasitism. The most common abnormalities were open wounds and parasitism by copepods. Tumors, lordosis, various fin disorders, popeye, fluid eye, cataract, blindness, parasitic leeches, and external and internal nematodes were also noted.
Goldfish were frequently caught from the river by anglers and accounted for 4% of the angler catch sampled in a 1977 creel survey (Harmon, Ref 2.2-52).
2.2.2.1.7.3.5 Swallowtail Shiner Peak spawning of swallowtail shiner (Notropis procne) occurred in mid-July in 1974 and in mid-June in 1976. Larvae were 4.8-5 mm at hatching and were identified in drift samples. However, because of difficulty in identification, this species was usually combined with other minnows in an "unidentifed minnow" category.
Young-of-year swallowtail were collected by seine as early as June (1971) and as late as September (1975).
Minnows accounted for 48, 78 and 25% of the total drift sample catch in 1974, 1975 and 1976, respectively. The mean density of drifting minnow larvae in 1974 was 0.21380/M3 , 0.0691/ms in 1975, and 0.1463/m 3 in 1976 (Table 2.2-23). Peak drift density occurred between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br />. Drifting minnow larvae were more abundant in the west channel than the east channel (Table 2.2-24) in 1975, and more abundant in the east channel in 1976. The distribution of larvae across the breadth of the river was also significantly different, with density being greater near shore. Push-net sampling conducted in 1976 (Table 2.2-26) 2.2-39
LGS EROL indicated minnow larvae abundance was greatest along the west shore, with high densities at stations S77161 (west shore),
S78973 (east shore), and S77970 (west shore).
The swallowtail shiner was one of the two most abundant minnows collected by seine, and comprised 56 and 32% of total seine catch in 1975 and 1976, respectively (Table 2.2-28). There was no significant difference in catch between years. In the 1975 seine collections it was most abundant prior to the spawning season (Figure 2.2-8). Few specimens were collected after May, indicating poor reproductive success, probably due to high water and increased turbidity, which occurred during frequent spates in June and July 1975. In 1976, the pattern was reversed and greatest catches were made late in the year; few specimens were collected prior to the spawning season (Table 2.2-29)..
Variation in catch between locations was significant in both 1975 and 1976. The greatest catches in 1975 occurred at S75730 (3566 specimens), and the fewest individuals were taken at S78900 (150). In 1976, the largest number was found at S76840 (1333),
the fewest were taken from S78460 (130), as shown in Table 2.2-30. Although catches were different between stations, analysis indicates that catches between all possible pairs of control and affected stations were significantly correlated.
Chironomid larvae were the most abundant food item in the identified.portion of stomach contents of river swallowtail shiner and comprised 77% of the material found in the stomachs that contained food. Chironomid pupae and adults were also important. The largest specimen collected was 70 mm FL.
2.2.2.1.7.3.6 Spotfin Shiner In the Schuylkill River, peak spawning of spotfin shiner (Notropis spilopterus) in 1974 and 1976 occurred in late-July, wereas in 1975 it occurred during the first half of August when water temperatures were 23 to 290C. Larvae were identified in river drift collections, but because of the difficulty in identification this species was usually combined with others in an "unidentified minnow" category (see swallowtail shiner).
Young-of-year were collected by seine as early as June (1973) and as late as September (1975).
The spotfin shiner was one of the two most abundant species collected by seine and represented 39 and 46% of the 1975 and 1976 catch, respectively (Table 2.2-28). There was no significant difference between 1975 and 1976 catches, but in both years significant variation in catch occurred between months. In 1975, the largest catches were made prior to the spawning season and few individuals were taken after May (Figure 2.2-9). In contrast, the greatest 1976 catches were made after spawning 2.2-40
LGS EROL occurred and few specimens were taken early in the year (Table 2.2-29). As discussed for the swallowtail shiner, frequent spates in June and July 1975 probably adversely affected spotfin shiner reproduction.
Variation in catch between locations was found to be significant in both years. In 1975, the catch ranged from 2728 individuals at S75730 to 173 at S78460. The greatest 1976 catch occurred at S76820 (1576 individuals), and the lowest at S76310 (291) as shown in Table 2.2-30.
Unidentified insect parts were found in 62% of all spotfin shiner stomachs containing food. Chironomids (larvae, pupae, and adults), terrestrial Coleoptera and Thysansoptera, composed the bulk of the summer diet. The maximum recorded length of a spotfin shiner was 86 mm FL.
2.2.2.1.7.3.7 White Sucker Breeding of white suckers (Catostomus commersoni) took place in the first half of May 1974, May through mid-June at temperatures of 12 to 240C in 1975, and late-April in 1976. Larvae had absorbed yolk sacs by the time they were 13-14 mm long. Larvae were often found in river drift, and in 1974 and 1976 were the sixth most abundant species; in 1975 they ranked second. Mean density of the white sucker drift was 0.0011/m 3 in 1974, contrasted to 0.0133/m 3 in 1975 and 0.0042/m 3 in 1976 (Table 2.2-23). Peak drift density generally occurred between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br />. In 1975, densities were greater along the west shore in 1975 and greater along the east shore in 1976 (Table 2.2-24).
Relative abundance of shoreline white sucker larvae, sampled by trap in 1975 (Table 2.2-25), differed from drift samples.
Young collected by seine were more abundant in 1976 than 1975 (Table 2.2-28). In both years most young were collected in June and were abundant at the mouths of Brooke Evans and Akm Run (S76820 and S77220), as shown in Table 2.2-30. Abundance of young at creek mouths indicated the importance of tributaries as white sucker spawning areas.
The white sucker was one of the most abundant large fish in the river, and comprised from 7 to 32% of large fish collected from 1973 to 1977. The mean standing crop of adult white sucker at Limerick sites A and B decreased between 1973 and 1975, but remained consistent from 1975 to 1977 -- 324 fish/ha was estimated in 1973, 203 in 1975, and 243 in 1977 (Table 2.2-37).
The standing crop at Firestone and Vincent Pool increased from 1974 to 1977. In the second half of 1976, the catch-per-unit-effort was significantly greater in October than in July, probably reflecting recruitment of young-of-year (Table 2.2-36).
2.2-41
LGS EROL Population size was generally greatest at Firestone, smallest at Vincent Pool, and intermediate at Limerick sites A and B (Table 2.2-37). Catch-per-unit-effort sampling in 1976 indicated that the white sucker was significantly more abundant at Firestone than at Vincent B (Table 2.2-36). Studies of Schuylkill fish have indicated that the white sucker prefers a fast water habitat, such as that at Firestone, and is less likely to be found in quiet water like that at Vincent Pool.
The mean biomass of white sucker at Limerick A and B varied in a manner similar to numbers (Table 2.2-37). The standing crop biomass in 1977 was greater at Firestone than at Vincent Pool.
In young white suckers examined, Cladocera and chironomid larvae were the most abundant food items, and were found in 64 and 62%,
respectively, of all stomachs containing food. Other important items included, in decreasing order of abundance, algae, copepods, chironomid pupae, tubificids, and chironomid adults.
Most specimens collected in 1973 were age II, the oldest age IV.
Greatest growth occurred during the second year (Table 2.2-38).
Length-weight relationships for these fish are presented in Table 2.2-39. The longest white sucker collected was 409 mm FL.
OAscoliosis, number of disorders were noted including open wounds, fungus; opercle deformity, numerous fin disorders, blindness, parasitic leeches, copepods, nematodes, and black spot. About 8.3% of white suckers collected were afflicted. Open wounds, parasitic copepods, and leeches were the most common maladies.
White suckers support a small spring fishery during their spawning run and are of some recreational importance.
2.2.2.1.7.3.8 Brown Bullhead In 1975, brown bullhead (Ictalurus nebulosus) spawned from early June to mid-July at temperatures of 21 to 250 C; peak spawning occurred in mid-June to early July. Larvae were rarely collected in the drift because of adult nesting behavior and parental care.
Most drift specimens were recently transformed juveniles, and density was generally low (Table 2.2-23). In contrast to other species, drifting brown bullheads were more abundant in midriver than along the shore (Table 2.2-24). No brown bullhead was collected along the shore in push-net samples.
Young were rarely collected by seine before 1977 (Table 2.2-28).
Preliminary inspection of 1977 seine collections indicated a large catch in excess of 500 individuals. This may have O represented the first successful spawn since 1971. Age and growth data indicated that the brown bullhead suffered virtual failure of the 1972 year class, probably due to the catastrophic 2.2-42
LGS EROL June 1972 flood and concomitant oil spill. Since that time, seine and small fish population estimate collections have indicated little or no production of young.
Brown bullheads comprised from 4 to 43% of the large fish population estimate catch from sites near LGS in 1973, 1975, and 1977. They were most numerous in 1974 at Limerick A, and least numerous in 1977 at Firestone (Table 2.2-32). The mean number of adults at Limerick sites A and B remained quite constant from 1973 to 1975, but dropped dramatically from 1975 to 1977 (Table 2.2-37). The standing crop at Firestone and Vincent Pool showed a similar decline. The substantial decrease was a result of the unsuccessful spawning discussed above.
In the second half of 1976, brown bullhead catch-per-unit-effort did not exhibit significant variation between months (Table 2.2-36). Mean population size was greatest at Vincent Pool (1468 fish/ha), least at Firestone (139/ha), and intermediate at Limerick sites A and B (419/ha). Brown bullheads prefer slow water habitats and were thus likely to be found in greater abundance at Vincent Pool than at Firestone. The mean biomass at Limerick A and B varied in the same manner as numbers (Table 2.2-37). Biomass at Firestone was much less than that at Vincent Pool.
Plant material (in 87% of stomachs containing food) and chironomid larvae (71%) and pupae (51%) were the most common items in the identifiable portion of bullhead stomachs from the Schuylkill River. Other food items, in decreasing order of occurrence, were plant material, insect parts, various aquatic organisms, terrestrial organisms and tubificids.
Age and growth of this species were studied in collections made from 1973 to 1975. The oldest individuals were age VIII. The greatest growth in length occurred in the first year of life (Table 2.2-38). Mean calculated lengths at annuli were slightly, but consistently, greater in 1975 than in 1973 to 1974. No differences were detected between sexes in all year-classes from 1973 to 1974. No population-wide difference in growth in length between Limerick A and B was detected from 1973 to 1974. The longest specimen collected from the river was 389 mm FL. Length-weight relationships for the collections are shown in Table 2.2-39. The rate of weight gain decreased with each successive year of life. No consistent difference in instantaneous growth was detected between sexes.
The age structure in late summer 1973 was characterized by a very small age-group I, dominant age-group II, and a strong age-group V. The population appeared quite stable, except for the weak age-group I. In 1975, a very strong age-group III dominated, and the lack of recent successful spawning was evidenced by very weak age-groups I and II (Figure 2.2-10).
2.2-43
LGS EROL
'M Specimens were commonly afflicted with disease or parasites; 8.6%
of specimens collected from 1974 through 1976 exhibited at least one disorder. Symptoms noted included open wounds, fungus, tumor, scoliosis, various fin disorders, cataract, blindness, leeches, parasitic copepods and nematodes, and yellow and white cyst. Maladies that occurred most frequently were open wounds and parasitic leeches.
A creel survey conducted in 1976 indicated that the brown bullhead was the preferred specie of anglers on the Schuylkill River (Harmon, Ref 2.2-52).
2.2.2.1.7.3.9 Banded Killifish In the river, peak spawning of banded killifish (Fundulus diaphanus) in 1974 occurred in mid-June, in 1975 from early July through early August, (at temperatures of 22 to 290 C) and in 1976, from late-June through mid-July. Larvae were identified in drift samples where they accounted for <1% of catch in 1974, 1%
in 1975 and <1% in 1976. Mean density was 0.0011 larvae/mn in 1974, 0.0012/m 3 in 1975 and 0.00005/m3 in 1976 (Table 2.2-23).
The greatest daily drift density occurred between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br />. Drift tended to be slightly more dense near shore in
- the east channel (Table 2.2-24). Few larvae were collected by shoreline trap sampling (Table 2.2-25) or push-net sampling (Table 2.2-26). Young-of-year killifish appeared in seine catches from early July (1971) to late September (1976).
The banded killifish ranked sixth in abundance in 1975 seine collections and accounted for <1% of the catch. In 1976, it ranked eighth and comprised 1% of the catch (Table 2.2-28). The small fish population estimate data also indicated an increase in abundance from 1975 to 1976 (Table 2.2-31).
Greatest seine catches of banded killifish in 1975 occurred early in the year. Low summer and fall catches indicated poor reproductive success. In 1976, large catches were made in August and July, probably reflecting recruitment of young; few were taken in other months (Table 2.2-29). The greatest number of banded killifish was taken from S75730 and S77960 in 1975; catches at other stations were generally low. In 1976, the greatest catches were made at S77960 and S76820 (Table 2.2-30).
In the Schuylkill, chironomid larvae and pupae were the most common food items in the stomachs of killifish. Chironomid adults and tubificids were also among gut contents.
The maximum length of banded killifish collected from the LGS A study area was 81 mm FL from East Branch Perkiomen Creek.
2.2-44
LGS EROL 2.2.2.1.7.3.10 Redbreast Sunfish Redbreast sunfish (Lepomis auritus) breeding took place in mid-July in 1974, and mid-June to early August in 1975 when water temperatures were 19 to 290 C. Eggs were demersal and loosely adhered to stones and gravel of the nest. Hatching occurred in 48 hours5.555556e-4 days <br />0.0133 hours <br />7.936508e-5 weeks <br />1.8264e-5 months <br /> at 220 C and larvae were 5.5-5.7 mm long. The yolk was absorbed in 3 to 4 days, when larvae had attained a length of 8 mm. Yolk-sac larvae remained in the general nesting area.
Post-larvae were found in vegetative shallows. Drifting redbreast sunfish larvae were not identified by species, but were included in a Lepomis spp. category. Also in this group were larvae of the pumpkinseed, green sunfish, and bluegill. This group ranked fourth in abundance in 1974, 1975 and 1976. Mean drift density in 1974 was 0.0350 fish/M3 , 0.0012/Mi3 in 1975 and 0.0196/m 3 in 1976 (Table 2.2-23). Larvae were collected in the drift from May through August in all three years. Peak drift density generally occurred between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br />. The density of drifting Lepomis spp. larvae was greater along the west shore in 1975 and greater along the east shore in 1976 (Table 2.2-24).
The relative abundance of shoreline Lepomis spp. larvae sampled by trap in 1975 agreed well with the relative abundance determined from drift samples (Tables 2.2-23 and 25). Most larvae were collected in August (1975). In 1976 push-net sampling, larvae of Lepomis spp. ranked third in abundance, and were collected from 11 of 13 stations (Table 2.2-26). Larvae were more abundant along the west shoreline and downstream of the proposed LGS discharge location (Table 2.2-27).
Population estimates of age 0 redbreast sunfish varied significantly from 1973 through 1976. Young redbreast sunfish were most numerous in 1974 and 1976, present in low numbers in 1973, and absent in 1975 (Figure 2.2-12). These data agreed well with seine collections. No significant variation in abundance of redbreast sunfish was detected between sites. Biomass estimates of young redbreast sunfish corresponded with changes in numerical abundance, exhibiting only an insignificant temporal variation.
The redbreast sunfish was the most abundant sunfish species collected in the large fish population estimate and catch-per-unit-effort sampling It accounted for 10 to 50% of the population estimate catch from 1973 through 1977 (Table 2.2-32), and 5 to 44% of 1976 catch-per-unit-effort catch (Table 2.2-33).
At the Limerick A population estimate site, the redbreast sunfish showed an increase in abundance from 1973 through 1977. At Limerick B however, population size was more constant (Table 2.2-37). Estimated number/ha at Firestone and Vincent Pool increased from 1974 through 1977.
2.2-45
LGS EROL W The redbreast sunfish was significantly more abundant at Limerick A than at Limerick B in 1975; no difference was detected in 1973.
Preliminary review of 1977 data indicated the redbreast sunfish was again more abundant at Limerick A. Since Firestone and Vincent Pool were not sampled in the same years as Limerick A and B, and since they were different in size, rigorous statistical analysis among all four sites was inappropriate. However, inspection of mean estimated number/ha at Firestone (550),
Limerick A (369), Limerick B (253), and Vincent Pool (240) indicated an obvious difference between sites, probably a result of different physical habitats (Table 2.2-37). Results of 1976 catch-per-unit-effort sampling also indicated differences between sites; the catch was significantly greater at Firestone and Limerick C than at Vincent B. Catch per unit effort values were generally greater in September and October, probably reflecting recruitment of young-of-year (Table 2.2-36).
Estimates of mean redbreast sunfish biomass at Limerick A and B varied in a manner similar to numbers (Table 2.2-37). The biomass at Firestone was greater than that at Vincent Pool.
Adult redbreasts from the Schuylkill were found to contain Hymenoptera adults, snails, other adult insects, and chironomid
.terrestrial larvae among their stomach contents. Aquatic insects and organisms were the most commonly occuring food items (Figure 2.2-11).
Greatest growth occurred in the second year of life (Table 2.2-38); after the first year, males grew faster than females. Based upon age and growth and population estimate data, most redbreast sunfish in the river appeared to be age II in 1973. In 1975, the age II group was consistently smaller than in 1973.
The length-weight relationships for 1973 and 1975 are shown in Table 2.2-39. Examination of instantaneous growth rates showed slower rates with each successive year of life, and higher rates in males.
Redbreast sunfish collected from the Schuylkill occasionally exhibited symptoms of disease, or were parasitized. Of the individuals collected from 1974 through 1976 2% exhibited at least one disorder. Symptoms of disease and parasites that were noted included open wounds, fungus, scoliosis, deformed opercle, various fin disorders, cataracts, eye flukes, blindness, parasitic leeches and copepods, yellow cysts, and internal nematodes. The maladies that occurred most frequently were parasitic copepods and open wounds.
- This species ranked first in abundance in angler catch from the Schuylkill River (Harmon, Ref 2.2-52).
2.2-46
LGS EROL 2.2.2.1.7.3.11 Pumpkinseed Pumpkinseed (Lepomis gibbosus) spawned during the same time period as redbreast sunfish. Nests were constructed among or near vegetation. Eggs loosely adhered to small stones or gravel in the nest. Larvae were approximately 3 mm long when hatched and absorbed their yolk in 5 to 7 days. Yolk-sac larvae remained in the general nesting area and juveniles inhabited vegetative shallows. See the redbreast sunfish for a description of Lepomis larvae population dynamics.
Population estimates of age 0 pumpkinseeds varied significantly from 1973 through 1976. Young pumpkinseeds were most numerous in 1974, and present in low numbers in 1973, 1975, and 1976 (Figure 2.2-12). Seine data confirmed the comparative absence of young pumpkinseeds in 1975 and 1976 (Table 2.2-28). Population size of pumpkinseed young-of-year did not vary significantly among sites. Biomass estimates varied in a manner similar to numbers.
The pumpkinseed was the second most abundant sunfish collected in the large fish population estimate and catch-per-unit-effort sampling in the Schuylkill River. It accounted for 1 to 39% of the population estimate catch from 1973 through 1977 (Table 2.2-32), and 3 to 21% of the 1976 catch-per-unit-effort catch (Table 2.2-33).
The river population of pumpkinseeds decreased steadily after 1973 (Table 2.2-37). Abundance dropped significantly between 1973 and 1975 at both Limerick A and B. A preliminary analysis has revealed that the number per hectare continued to fall through 1977. The estimated number per hectare also decreased at Vincent Pool.
In both 1973 and 1975, the pumpkinseed was significantly more abundant at Limerick B than Limerick A. Preliminary analysis of 1977 data indicated that the same was true in that year. Since Vincent Pool was not sampled in the same years as Limerick A and B, and was also of different size, rigorous statistical analysis between all three areas was inappropriate. However, inspection of the mean estimated number per hectare at Limerick A (55),
Limerick B (147), and Vincent Pool (263) revealed obvious spatial variation, probably habitat-related. Interestingly, the pumpkinseed and redbreast sunfish numbers have varied in an opposite manner, both spatially and temporally.
Within the latter half of 1976, the pumpkinseed catch-per-unit-effort was generally greatest in September and October, probably reflecting recruitment of young-of-year (Table 2.2-36). No significant spatial variation in pumpkinseed catch-per-unit-effort was detected in 1976.
2.2-47
LGS EROL The biomass at Limerick A and B varied correspondingly with number estimates. Estimated biomass at Vincent Pool (1977) was 3.7 kg/ha (Table 2.2-37).
Pumpkinseeds feed on chironomid larvae and pupae, plant material, snails, terrestrial insects, and numerous other items.
No pumpkinseed older than age IV were collected at Limerick A and B in 1973 and 1975. In 1973, the greatest growth occurred in the first year, while in 1975 most growth took place in the second year (Table 2.2-38) Growth at Limerick B was greater in 1973 than in 1975. Length-weight relationships (Table 2.2-39) were not significantly different between sites in 1973, but were in 1975.
Data from both years indicated that instantaneous growth decreased with each succeeding year of life.
The age structure of the pumpkinseed in 1973 was characterized by a dominant age-group II and a very weak age-group I, while the 1975 age structure appeared stable, with no obvious dominant or weak age groups (Figure 2.2-13).
Pumpkinseeds collected from the river were frequently diseased or parasitized; 11% of specimens collected from 1974 through 1976 were afflicted with at least one disorder. Symptoms of disease and parasites noted included open wounds, fungus, various fin disorders, eye flukes, blindness, parasitic leeches and copepods, external nematodes, black spots, yellow and white cysts, and internal nematodes. Maladies that occurred most frequently were parasitic copepods and internal nematodes.
The pumpkinseed was frequently caught by recreational anglers on the Schuylkill (Harmon, Ref 2.2-52).
2.2.2.1.7.3.12 Largemouth Bass The largemouth bass (Micropterus salmoides) was common in the river, but larvae were rarely collected in drift samples. It was assumed that, because of parental care, larvae of this species seldom drift. No larvae were collected in 1976 push-net sampling. Young bass were infrequently collected from the Schuylkill by seine or the small fish population estimate sampling (Tables 2.2-28 and 31).
The relative abundance of largemouth bass in large fish collections decreased from 1973 through 1977. In 1973, they made up nearly 3% of the catch from two sites near LGS, but dropped to 1% in 1975. Only one individual was captured from each of these sites in 1977 (Table 2.2-32). Estimates of the standing crop of largemouth bass were made only for Limerick A and B in 1975. The estimated number per hectare was six at Limerick A and eight at Limerick B. Biomass estimates were 1.1 kg/ha for both sites.
2.2-48
LGS EROL A study of food habits of 7 river largemouth bass, 48 to 98 mm FL, revealed that fish were the primary food item. Larval fish were found in 43% of the stomachs containing food, cyprinid (39%), fish remains (29%), and centrarchids (14%). Other items identified were chironomid pupae, terrestrial Hymenoptera, and tubificids.
The longest largemouth captured from the Schuylkill was 351 mm FL. Of 103 specimens collected in 1973, only 17 were older than age 0 and none was older than age III. Mean calculated lengths at annuli I, II, and III were 90, 126, and 242 mm FL, respectively (Table 2.2-38). The small sample size made comparison of growth by year difficult. Age structure of largemouth bass in 1973 showed young-of-year fish were dominant, comprising 92% of fish collected.
Largemouth bass occasionally exhibited symptoms of disease or parasitism. From 1974 through 1976, 2% of largemouth bass collected were afflicted with at least one malady. Symptoms included open wounds, various fin disorders, parasitic copepods, yellow cyst, and "bass boils." Parasitic copepods were the most frequently observed disorder.
The largemouth bass was infrequently caught by anglers on the river, but was actively sought by some fishermen (Harmon, Ref 2.2-52).
2.2.2.1.7.3.13 Tessellated Darter Spawning of tessellated darter (Etheostoma olmstedi) occurred from May through June at temperatures of 12 to 240C. Larvae were 4 to 5 mm long upon hatching and were usually found among shallow vegetation. Larvae accounted for 1.6% of the total catch in 1975 and <1% in 1976 (Table 2.2-23). Most larvae were collected in May, and peak drift density occurred between 2200 and 0500 hours0.00579 days <br />0.139 hours <br />8.267196e-4 weeks <br />1.9025e-4 months <br />.
Drift density was greater along the east shore (Table 2.2-24).
Few larvae were collected in trap or push-net samples along the shoreline, and only in May 1976 (Tables 2.2-25 and 26).
The tessellated darter ranked eleventh in abundance in 1975 seine collections , and made up <1%, of the total catch. Abundance increased in 1976 when the species ranked seventh and accounted for 2% of the catch (Table 2.2-28). Data collected in small fish population estimate sampling also indicated an increase in abundance from 3% of the catch in 1975 to 10% in 1976 (Table 2.2-31).
Greatest seine catches in 1975 occurred in February; very few individuals were collected in any other month. In 1976, the greatest numbers were collected in June and July, with few specimens taken from February through March (Table 2.2-29). The 2.2-49
LGS EROL W most individuals collected were from S76840 in 1975 and S75730 in 1976 (Table 2.2-30).
Tessellated darters in the river fed primarily on Cyclopidae and chironomid larvae. Other food items were cladocerans and isopods.
The maximum length of tessellated darters collected from the study area was 78 mm FL, from East Branch Perkiomen Creek.
2.2.2.1.8 Trophic Relationships The stability of perpetuating assemblages of organisms is due largely to nutritional relationships among component populations.
Assessment of the trophic organization is necessary for an adequate understanding of the roles of individual species and biotic components in the ecosystem.
A generalized diagram (Figure 2.2-14) was constructed to summarize the structure and function of selected biotic components within the LGS study area. The representative
. organisms pictured are important in one or more of the three river systems. Construction of trophic pathways was based largely upon literature, although some studies of food habits were conducted by the Applicant's consultant. Phytoplankton (primarily of periphytic origin) and zooplankton were present in low densities in all systems and therefore were not included.
Benthic diatoms and detritus presumably provide the main food base in all systems. Detritus, whether derived from within the stream (autochthonous) or surrounding watershed (allochthonous),
is any nonliving organic matter that has begun to be utilized by microconsumers (bacteria, fungi, and, protozoa). Diatoms and the filamentous green alga Cladophora were important primary microroproducers and macroproducers, respectively, in the river and both creeks. Macrophytes (e.g., Myriophyllum) were seasonally abundant primary producers in the river.
Macroconsumers include invertebrates and fish. Invertebrates exhibit a wide variety of feeding mechanisms. Cummins (Ref 2.2-61) partitioned them into four functional groups, all of which are represented by species important within the study area:
(1) grazers and scrapers (e.g., mayflies, beetles, and snails) -
large herbivores feeding on attached algae and associated mineral and detritus deposits; (2) shredders (e.g., stoneflies, craneflies, and crayfish) - large particle feeding detritivores; (3) collectors (e.g., caddisflies, blackflies, and midges) - both
- suspension (filter) and deposit (surface) fine particle feeding detritivores; and (4) predators (e.g., hellgrammite, and midges)
- carnivores.
2.2-50
LGS EROL Lagler et al. (Ref 2.2-62) partioned fish into four general feeding types, three of which were represented by important species within the study area: (1) predators (e.g., muskellunge and brown bullhead), (2) grazers (e.g. Redbeast sunfish and pumpkin seed), and (3) suckers (e.g., white sucker.)
Cummins (Ref 2.2-60) stated that ecological communities follow a transition from headwater to higher order streams that involves both producers and consumers and, further, that transition in organic inputs and plant growth undoubtedly represents the basis of changing overall community structure and function. In general, headwater streams like East Branch Perkiomen Creek are characteristically more dependent upon terrestrial contributions of particulate organic matter, especially coarse particles such as leaf litter. There is evidence that allochthonous input is also important to the Schuylkill River near LGS because the river is measureably heterotrophic most of the year.
2.2.2.2 Perkiomen Creek Perkiomen Creek is located in the Triassic Lowland section of the Piedmont physiographic province, a rich farming area of rolling hills. It is a major Schuylkill tributary in this province and drains 938 km 2 of Lehigh, Berks, Bucks, and Montgomery counties.
The aquatic community of the Perkiomen Creek system has been influenced by man's long history of activities in the watershed.
Water quality and flows have been altered, habitats changed or eliminated, and the species complex directly manipulated.
Although these activities have probably reduced diversity somewhat, the community remains relatively stable and healthy.
The creek downstream of the East Branch confluence will be impacted by water diversion; water withdrawal will occur at Graterford. The Perkiomen Creek study area includes that stretch from Spring Mount Road bridge downstream to below the U.S. 113 bridge (Figure 2.2-15). For a further description of this area, refer to Section 6.1. Sample stations are designated by common name and by the letter 'P' followed by a number that indicates distance in meters from the mouth of the creek. Where stations include several meters of stream, site numbers designate the downstream end of the station.
Aquatic biota of the Perkiomen Creek study area was extensively studied by the Applicant's consultant from 1970 through 1978. A summary of sampling history by program is given in Tables 2.2-40 and 2.2-41.
2.2-51
LGS EROL 2.2.2.2.1 Water Quality and Environmental Stress Perkiomen Creek is a major tributary to the middle reach of the Schuylkill River. Its relatively rural watershed contains a number of small boroughs, but no major population centers. Most surrounding land is residential or used for agriculture. Low base flows and frequent spates characterize an extremely variable flow regime. Spring flows are generally high due to snow melt and precipitation; late summer and early autumn flows are very low, but subject to rapid fluctuation due to local thunderstorms.
Water quality near Graterford is relatively good, with nutrient loading being the most serious stress (Section 2.4). Nutrients enter the stream from both point and nonpoint sources, and from Green Lane Reservoir. Primary point sources are municipal sewage treatment plants. Nonpoint source nutrients originate from onsite sewage treatment facilities and from agricultural runoff.
Green Lane Reservoir also receives point and nonpoint source nutrients. Of 17 Pennsylvania lakes inventoried by the EPA's National Eutrophication Survey in 1973 and 1974, Green Lane was found to be most eutrophic (DVRPC and Chester-Betz Engineers, Ref 2.2-15). Water released from the hypolimnion during summer stratification is anoxic, and highly enriched with nutrients.
2.2.2.2.2 Phytoplankton A qualitative study of phytoplankton in 1974 (Tables 2.2-40 and 41) yielded 54 taxa (Table 2.2-42). Diatoms were represented by 22 genera and were found throughout the year. Green and blue-green algae were represented by 25 and 6 genera, respectively, and were found predominantly in summer and early fall. Seasonal succession of these three groups in Perkiomen Creek followed seasonal changes in water temperature, and was similar to that previously described for the Schuylkill River (Section 2.2.2.1.2).
The benthic diatom Navicula was the most common phytoplankter, and occurred throughout the year; it was particularly abundant in the winter. The planktonic diatom Melosira was abundant in late summer. Three genera (Ankistrodesmus, Scenedesmus, and Pediastrum) of green algae were abundant phytoplankters; all were present in low numbers in winter and spring, and increased in the summer. Anabaena was the only abundant genus of blue-green algae and was most common in the summer.
In general, phytoplankton densities in Perkiomen Creek appeared to be low, and the most abundant phytoplankters were of periphytic
- origin. For these reasons, Perkiomen Creek was considered to be an area of low potential impact for phytoplankton.
2.2-52
LGS EROL 2.2.2.2.3 Periphyton Periphyton, an important primary producer in Perkiomen Creek, was studied from July through December 1973 (Tables 2.2-40 and 41).
Taxonomic composition was very similar to that in the East Branch (Section 2.2.2.3.3), and was almost exclusively diatoms.
Maximum standing crop biomass (106 mg. dry wt/dm2 ) and production rate (8 mg dry wt/dm2 /day) were recorded in October; lowest values for both parameters occurred in December (Table 2.2-43).
2.2.2.2.4 Macrophytes Macrophytes were not studied in Perkiomen Creek. Qualitative observations indicated that macrophytes were not common, and they were therefore considered to be of low potential impact.
2.2.2.2.5 Zooplankton Zooplankton was not studied in Perkiomen Creek because it was considered to be of low potential impact. Studies conducted in other temperate small streams have shown that zooplankton is typically low in density.
2.2.2.2.6 Macroinvertebrates Benthic macroinvertebrates play an important functional role in most lotic ecosystems by converting allochthonous and autochthonous materials into temporary storage within their own tissue, thus ultimately becoming an essential component in the food web. Macroinvertebrates also shred coarse organic material (e.g., leaves) into finer particles that can be utilized by smaller macroinvertebrates.
A pilot study was conducted in Perkiomen Creek and East Branch Perkiomen Creek from June 1970 through December 1971. Data collected during this period were used to develop an experimental design for a preoperational quantitative program that began in January 1972, and was continued in 1973, 1974, and 1976. Only the riffle biotope was sampled quantitatively; it was common in the creeks, and invertebrate diversity and production are typically highest in this type of habitat. Pilot study data, because of their qualitative nature, were used only in the compilation of a species list. Qualitative collections were also made periodically in 1972 and 1973 to aid in compiling a comprehensive species list for each location.
2.2-53
LGS EROL
, Two locations were sampled on Perkiomen Creek (Spring Mount station - P22000, above the East Branch confluence; Rahns station
- P13600, below the confluence), and 6 on East Branch Perkiomen Creek (Elephant station - E36725, Branch station - E32200, Sellersville station - E26700, Cathill station - E23000, Moyer station - E12500, WaWa station - E5600). For a summary of Perkiomen Creek and East Branch Perkiomen Creek macroinvertebrate sample history, see Tables 2.2-40 and 41, and Tables 2.2-70 and 71 respectively.
2.2.2.2.6.1 Species Inventory A species list (Table 2.2-44) of macroinvertebrates collected by all methods (i.e., benthos quantitative and qualitative, and drift) indicated that both creeks were characterized by a diverse macroinvertebrate assemblage. Representatives of all major orders of aquatic insects were collected between June 1970 and December 1976, as were planarians, annelids, isopods, amphipods, decapods, mollusks, and others. The more diverse groups were Arthropoda (82% of total taxa, of which 96% were insects),
Annelida (8%; 48% leeches, 32% worms, and Mollusca (6%; 58%
snails, 42% clams). The more diverse insect orders were Diptera,
- Coleoptera, Trichoptera, and Ephemeroptera. Diptera was represented by the greatest number of families and one family, Chironomidae, contained the greatest number of genera. Of the 301 taxa collected, 15 were considered abundant, 65 common, 97 uncommon, and 124 rare.
Designation of abundance (abundant, common, uncommon, rare) for taxa on this list was highly subjective, particularly for non-riffle organisms. Abundance was based on field observation and range within each Creek. Seasonal fluctuations were not considered. For example, a taxon was considered "rare" if only a few specimens were collected. A taxon present in high densities at only one or two stations were considered "uncommon" as was a taxon present throughout the study area but in low numbers. A cosmopolitan taxon present in high numbers was termed "abundant".
Other taxa were considered "common".
2.2.2.2.6.2 Community Description Based upon quantitative sampling of the riffle biotope, it was apparent that longitudinal changes in macrobenthos in East Branch Perkiomen Creek were strongly influenced by intermittent flow in the headwaters and degraded water quality in the middle section.
Benthic invertebrates exhibited a high degree of resiliency in response to short-term phenomena such as spates and localized channelization. There were no major anthropogenic stresses 2.2-54
LGS EROL operating in that section of Perkiomen Creek included in the study area, and diversity (richness) was greater here than in the East Branch.
Faunal patterns, with few exceptions, were relatively constant as relative abundance data showed little variation between years.
All forms of feeding mechanisms were represented among the dominant invertebrates as were primary, secondary, and tertiary consumers. Macrobenthos communities in both creeks were diverse and productive.
2.2.2.2.6.2.1 Standing Crop Numbers and Biomass For both creeks, numerical and biomass standing crop data were highly variable between sites in the same month, and between months within a year for the same site. When data from all months were combined and averaged by year, spatial trends in abundance were apparent (Table 2.2-45). Intermittent flow and degraded water quality reduced standing crop numbers in the upper (Elephant 4-year mean, 5736 organisms/m2 ; Branch, 8339/M2 ) and middle East Branch (Sellersville 8277/M 2 , Cathill 6578/M 2 ),
respectively. Recovery, in terms of increased density, was evident in the lower section (Moyer 14,925/M2 , WaWa 23,781/M 2 ).
Standing crops in Perkiomen Creek averaged 14,996/M2 at Spring Mount, upstream of the confluence, and 12,906/M2 at Rahns, downstream of the confluence. Spatial trends in biomass density in both creeks were like those for numbers; biomass at Cathill was particularly low in 1973 and 1974 due to the preponderance of small-size chironomid larvae.
In general, both Perkiomen Creek stations (Table 2.2-45) and the East Branch, all stations combined (numbers Table 2.2-46); and biomass (Table 2.2-47), showed an increase in benthic density in all consecutive sample years. The marked increase in mean density in the East Branch between 1974 and 1976 was due largely to the increase in the fingernail clam Sphaerium rhomboideum at WaWa. Although 1972 was the year of Tropical Storm Agnes (greatest flood of record), invertebrate density was reduced below normal only in June and there was little effect on the annual mean.
Within-year trends in total standing crop largely reflected the population dynamics of dominant organisms (described below under "Important Species"). In general, total numbers and biomass were greatest in the fall (Table 2.2-48).
2.2-55
LGS EROL 2.2.2.2.6.2.2 Richness The taxonomic diversity (richness component) of riffle benthos was high in both creeks throughout the year. In the East Branch of Perkiomen Creek, annual diversity (Table 2.2-45) was highest at upstream stations (Elephant 4-year mean, 59 taxa; Branch, 55 taxa), decreased at Sellersville (52 taxa), and reached a low midpoint in the creek at Cathill (32 taxa). Diversity then increased with increasing distance downstream (Moyer, 46 taxa; WaWa, 47 taxa) but did not recover to levels found in the headwaters.
High richness at Elephant was due in large part to intermittent flow, which typically occurred in late summer and fall. Surface flow often ceased during this period, and the riffle habitat was replaced temporarily by isolated pools maintained by subsurface percolation. This change to a pool habitat, still effectively sampled, was accompanied by an invasion of quite water species, primarily of the groups Hemiptera and Coleoptera. The relatively large fluctuations in total taxa collected between years at Elephant, and perhaps Branch, may have been related to the intensity and duration of discontinuous flow.
. Diversity at Sellersville was below that at Branch, but was still relatively high. This station was sporadically subjected to storm sewer discharge from two pipes under the Main Street Bridge. Quantitative sampling transected the entire channel directly downstream of the bridge at this site, and both affected and unaffected areas were sampled. The relatively high diversity here may not indicate an entirely healthy environment, but rather a diverse set of water quality conditions.
The reduction in benthic richness at Cathill was due to the station's continual exposure to the Sellersville Borough sewage treatment plant effluent (Section 2.2.2.3.1). A zone of recovery extended the remaining length of the creek.
The annual total number of taxa collected in the East Branch, all stations combined, decreased slightly from 1972 to 1974, but increased to a maximum in 1976 (Table 2.2-46). This variability reflected: (1) annual variation in the intensity of perturbations already discussed (i.e., intermittency and effluent degraded water quality), as well as short-term stresses such as spates at all stations, stormwater input at Sellersville, channelization at Branch in June 1974, etc; (2) decrease in sample size from 5 to 4 replicates in July 1973, in general more uncommon taxa are collected as 'n' increases; and (3) absence of sampling in winter 1974. The June 1972 flood had little effect on annual diversity.
- Benthic diversity was greater in Perkiomen Creek than in the East Branch, and slightly greater above the confluence (Spring Mount,
- 68) than below it (Rahns, 63) as shown in Table 2.2-45. Flow at 2.2-56
LGS EROL Spring Mount was near torrential, substrate was mixed rubble and supported an epilithic algal community for much of the year.
Flow at Rahns was more laminar, and the compacted sand-gravel substrate (overlain by a few large rocks) was susceptible to scouring during high-water periods.
2.2.2.2.6.23 Similarity Between Stations Monthly computation of Morisita's index of overlap (Brower and Zar, p. 144, Ref 2.2-75) provided a single value denoting benthic community similarity between selected pairs of stations in terms of taxonomic composition and abundance; the higher the value (range 0-1) the more similar. Yearly means were determined by averaging all monthly values within the year. Similarity between adjacent sites in East Branch Perkiomen Creek, excluding Chironomidae, ranged from lows of 0.426 and 0.431 (4-year means) between Cathill and Moyer and Elephant and Branch, and respectively, to 0.675 between Moyer and WaWa (Table 2.2-45).
Mean index values for the East Branch, all stations combined, were very similar in all years but 1976 (1972, 0.594; 1973, 0.583; 1974, 0.558; 1976, 0.367). Monthly variability was high.
Similarity between the two Perkiomen Creek stations was higher (0.727) than that for any East Branch pair.
In addition to computing Morisita's index of overlap between adjacent stations, all East Branch sites were compared individually with Moyer-station. The East Branch shows pronounced longitudinal differences in macrobenthos due primarily to intermittent flow in the headwaters and degraded water quality midpoint in the creek. Moyer is considered (on the basis of flow regime, substrate composition, faunal assemblage, and magnitude of stress as described in Section 2.2.2.3.1) to be the site that presently is most indicative of what more (in terms of length of stream) benthos may be like after diversion. East Branch pairings with Moyer gave the following 4-year mean values, in decreasing order; WaWa (0.675, most similar), Branch (0.598),
Sellersville (0.493), Cathill (0.425), and Elephant (0.367, least similar). It is expected that similarity between stations will increase following diversion, as flow and water quality conditions become more similar throughout the creek.
Overlap values that included Chironomidae (not shown) were higher in all instances due to the abundance of this group at all sites.
These values overestimated similarity in one sense, because the taxonomic composition of Chironomidae was known to differ, in some cases markedly, between stations.
2.2-57
LGS EROL 2.2.2.2.6.3 Important Species Within-year and between-year trends in standing crop largely reflected the population dynamics of dominant organisms.
Dominant species (taxa in this case, since not all macroinvertebrates were identified by species) were defined as those organisms, collected in quantitative benthic samples, that comprised 2% or greater of the total number or biomass for the station and year under consideration. Because of their high relative and absolute abundance, they were largely responsible for biotic interactions within the community, and hence were considered important (see Section 2.2) to existing community structure, function, and stability. Dominant (important) taxa were selected for each station, as well as for all East Branch stations combined, because benthic communities differed along the creeks, and a gradational spatial response to diversion is anticipated.
Taxa meeting this criterion were: (1) numbers only - Caenis sp.,
Tricorythodes sp., Perlesta placida; and Leucotrichia pictipes, (2) biomass only - Erpobdella punctata, Cambarus bartoni, Orconectes limosus, Argia spp., Corydalus cornutus, and Tipula spp.; and (3) numbers and biomass - Dugesia spp.; Oligochaeta, Ephemerella spp., Baetis spp., Stenonema spp., Allocapnia spp.,
Corixidae, Psephenus herricki, Stenelmis spp., Chimarra spp.,
Cheumatopsyche spp., Hydropsyche spp., Simuliidae, Chironomidae, Physa acuta, and Sphaerium spp. These 26 taxa represented 19% of the total number (139) of taxa collected in quantitative benthic samples during the 4-year study period.
The temporal (Table 2.2-48) and spatial (for numbers, see Table 2.2-49 and for biomass table 2.2-50) distribution of these taxa during the 4-year study period are discussed in phylogenetic order below. General trophic status is also indicated.
2.2.2.2.6.3.1 Dugesia spp.
Two species of this flatworm were found in the creeks, D.
dorotocephala and D. tigrina, with the former by far the more abundant. D. dorotocephala is eurythermic, tolerant of moderate organic pollution, and has an ecological preference for headwaters. D. tigrina is a eurythermic species occurring in the lower stretches of rivers. Both species are carnivorous and feed on living, dead, or crushed animal matter.
Dugesia (primarily D. dorotocephala) was present in the creeks in all months, but attained maximum densities in August through November. It was dominant at Branch, Sellersville, Moyer, and WaWa (the station of maximum numbers and biomass) and essentially absent at Cathill. D. tigrina was found in Perkiomen Creek and was dominant at Spring Mount.
2.2-58
LGS EROL 2.2.2.2.6.3.2 Oligochaeta Four families comprised the majority of numbers or biomass of benthic oligochaetes; Lumbriculidae, Naididae, Tubificidae, and Lumbricidae. The first three are strictly aquatic, whereas Lumbricidae is almost entirely terrestrial. Lumbricids were only found occasionally in samples from all stations, but their relatively large size made them important contributors to total worm biomass.
Lumbriculids were common at all stations except Elephant and Cathill, and their density appeared to be inversely correlated with tubificid density. Two types were encountered, one with simple setae (common) and one with bifid setae (rare). This family was more abundant in Perkiomen Creek than in the East Branch. They are intermediate in size between Lumbricidae and Tubificidae.
Naididae was found principally at Sellersville and to a lesser extent at Cathill. Species identified were Ophidonais serpentina, Nais communis, Pristina breviseta, and P. foreli.
These worms were periodically abundant in benthic samples, but because of their small size (about 3 mm) contributed little to standing crop biomass.
Tubificids (sludge-worms) were found at all stations, but occurred in greatest abundance at Sellersville and Cathill.
Species identified were Limnodrilus hoffmeisteri, L. claparedianus, Branchiura sowerbyi, Peloscolex ferox (Elephant station only), and Aulodrilus limnobius. Increased numbers of tubificids in the vicinity of organic effluents is well documented and can be attributed mainly to the adaptation of the respiratory physiology of the worms to very low oxygen concentrations, or even anaerobic conditions. Some tubificids (including L. hoffmeisteri) have high tolerance limits for lead and zinc in solution. Riffle is not the optimum habitat for either Tubificidae or Naididae, since both prefer fine sediments in which to burrow and feed.
In the creeks, oligochaetes were dominant at all sites but WaWa, and reached maximum densities at Sellersville. They were collected year-round and there were no obvious seasonal trends in abundance. Except for day-active Naididae, oligochaetes were not often collected in drift. As a group, oligochaetes are sediment ingestors deriving most if not all of their nutrition from bacteria.
2.2.2.2.6.3.3 Erpobdella punctata This is one of the most commonly encountered and widely distributed species of freshwater leeches in North America. It 2.2-59
LGS EROL
' is both predator (primarily oligochaetes and insect larvae) and scavenger. This leech is associated with polluted conditions.
It was found in low numbers at all stations and was dominant in terms of biomass only at Sellersville. Individuals were present year-round, with the highest numbers present in summer and fall.
2.2.2.2.6.3.4 Cambarus bartoni and Orconectes limosus Crayfish are principally omnivorous scavengers, seldom predaceous. They were most numerous and most often taken at Elephant station, and were taken sporadically and in low numbers at other stations. Only one, two and three individuals were collected at Cathill, WaWa, and Rahns stations, respectively, in the study -period. C. bartoni was the abundant species in the upper 10 km of East Branch Perkiomen Creek, whereas 0. limosus was essentially the only species inhabiting riffle habitat in the lower 26 km and in Perkiomen Creek. Crayfish were not abundant numerically but were often important contributors to biomass, particularly at upper East Branch stations.
Discontinuous flow was less severe in 1973 and 1974, and this may account for the higher crayfish densities in those years at
. Elephant station. The sampling method provided reliable estimates of crayfish density in riffle habitat; crayfish prefer to secrete themselves during the day under stones, and stones of appliciable size were routinely included within the sampling unit.
2.2.2.2.6.7.5 Caenis spp.
No key to the immatures of this mayfly genus exists, but only one species appeared to be present. Caenis appears to be more tolerant of low dissolved-oxygen concentration than any other mayfly. Like Tricorythodes, its preferred habitat is in those areas of streams that have greatly reduced current or no current, so their abundance in the creeks is probably greatest in non-riffle habitats. Feeding habits of nymphs are like those of Tricorythodes. Caenis was found at all stations, but was dominant only at Branch. Maximum densities occurred in September through November.
2.2.2.2.6.3.6 Tricorythodes sp.
No key to the immatures of this mayfly genus exists, but only one species appeared to be present. Nymphs are fairly common among gravel in permanent streams. Nymphs are detritivore-herbivore
- (active scrapers). Tricorythodes is a night-active drifter. It was rarely collected on the East Branch, but was numerous on 2.2-60
LGS EROL Perkiomen Creek, particularly at Rahns. It was generally found only in June through October, and was most abundant in September.
2.2.2.2.6.3.7 Ephemerella spp.
Three species of this mayfly were found in the creeks but only E.
deficiens was common. It is associated with vegetation in rocky, swift, unpolluted streams. Nymphs are herbivorous. Rarely taken on the East Branch, Ephemerella was dominant at both Perkiomen Creek stations. It was present in all months, but attained the highest densities in May, and July through December.
2.2.2.2.6.3.8 Baetis spp.
At least five species of Baetis mayflies were found in the creeks. The only numerous species keyed to B. intercalaris in Burkes (Ref 2.2-22). Baetis is common in shallow running water under stones, or among debris or emergent vegetation along the banks of brooks or creeks. With few exceptions nymphs are herbivores or scavengers, living on vegetable detritus and minute aquatic organisms, principally diatoms. Baetis spp. were dominant at all stations except Elephant and Cathill (essentially absent), and Moyer. Maximum densities occurred in May through September. Baetis spp. were commonly collected in drift samples, and were night-active.
2.2.2.2.6.3.9 Stenonema spp.
Eight species of Stenonema mayflies were found, three of which were commony collected; Stenonema (=Stenacron) interpunctatum at Elephant, and S. nepotellum and S. rubrum on Perkiomen Creek.
The S. (=Stenacron) interpunctatum complex is at present only superficially known and contains several subspecies; ours appeared to be S. (=Stenacron) interpunctatum heterotarsale. All three species are considered facultative and herbivorous.
Maximum densities occurred in the fall. Stenonema was common in drift, and night-active.
2.2.2.2.6.3.10 Argia spp.
No regional key to species based upon the immature stage is available, but apparently at least two species of this damselfly were present, one of which was rare. The common species keyed to A. apicalis in Walker (Ref 2.2-76). The carnivorous nymphs occur commonly in streams where they cling to rocks and debris in the current. Argia was collected at all stations, and was dominant at Branch (in both numbers and biomass). Maximum densities occurred in the fall.
2.2-61
LGS EROL 2.2.2.2.6.3.11 Allocapnia spp.
Several species of Allocapnia were founded in the creeks, but the common one was A. vivipara, found in greatest numbers at Elephant. It is a small, dark, brachypterous stonefly that emerges in mid-winter (hence the common name of winter stoneflies). It can be abundant in temporary streams, and feeds (chewing) on detritus and algae and is most abundant in allochthonous debris. Allocapnia was found in the upper East Branch and in Perkiomen Creek. Greatest densities occurred at Elephant in November through February. Nymphs were uncommon from April through October.
2.2.2.2.6.3.12 Perlesta placida This stonefly has a wide tolerance for different types of streams, including intermittent ones. It is also one of the few stoneflies that emerges in mid and late summer. It is strictly carnivorous (chewing) and feeds principally on ChirQnomidae, Ephemeroptera, and other insects. P. placida was found in the upper East Branch and in Perkiomen Creek. Greatest densities were at Elephant in April through June. Nymphs were essentially absent the rest of the year.
2.2.2.2.6.3.13 Corixidae The preferred lotic habitat of corixids, or water boatmen, is in pools and quiet regions of streams. They were collected in high numbers in quantitative samples only at Elephant during extremely low flow periods, when the riffle habitat was temporarily replaced by standing water. All instars of Sigara modesta were often abundant in these pools, coexisting with small numbers of Trichocorixa calva, a species with which it is commonly found (Bobb, Ref 2.2-74). As herbivores, corixids are unique among aquatic Hemiptera.
2.2.2.2.6.3.14 Corydalus cornutus C. cornutus (the adult is commonly called the dobsonfly, the larva the hellgrammite) is associated with larger components of substrate in riffle-run areas of well-aerated streams. The larva is a large (to 80 mm) and active macropredator that feeds mainly on Simuliidae, Hydropsychidae, and Chironomidae. It was rare in East Branch Perkiomen Creek, but dominant (in biomass) in Perkiomen Creek. Numerical densities were similar, and low throughout the year.
2.2.2.2.6.3.15 Psephenus herricki 2.2-62
LGS EROL Larvae of this beetle, known as 'water pennies' because of their flat and highly streamlined form, are aquatic and actively feed on algae and microcrustaceans. They exhibit a very strong positive thigmotaxis and prefer a riffle habitat. They were collected at all stations inthe study period, but were most numerous in the lower East Branch and at Rahns (station of maximum density) in Perkiomen Creek. Maximum larval densities occurred in October, and December and adults were collected incidentally in June through September.
2.2.2.2.6.3.16 Stenelmis spp.
Three species of this beetle were found in the creeks, but only one was abundant, probably S. crenata. Stenelmis is common in the gravel substrate of streams, and both larvae and adults are aquatic herbivores. Adults, unlike larvae, showed a propensity to drift and exhibited a nocturnal behavioral periodicity.
S. crenata has been recorded as tolerant of chlorides but sensitive to sewage and phosphate wastes.
Stenelmis was abundant in the creeks and was dominant at all but the Cathill and Spring Mount stations. Larvae were present in high densities April through November. Adults, like larvae, were collected in year-round but were most numerous in June through November.
2.2.2.2.6.3.17 Chimarra spp.
Two species of this caddisfly occurred in the creeks; C. aterrima, which was rare, and C. obscura, which was abundant.
C. obscura is the most widely distributed of the genus. It inhabits flowing water and constructs fixed retreats on the undersides of rocks in riffles that consist of elongate, saclike capture nets in which the larvae dwell and trap drifting food particles, generally smaller-sized particles than co-existing Hydropsychidae (e.g., Cheumatopsyche and Hydropsyche).
Chimarra was abundant in the creeks and was dominant at most stations. It was uncommon at Elephant and Cathill. Larvae were most numerous in late summer and fall; pupae were collected from April through December, and peak numbers occurred in July through September. At least some instars drifted and exhibited a nocturnal periodicity.
2.2.2.2.6.3.18 Cheumatopsyche spp. and Hydropsyche spp.
These two genera of closely related net-building caddisflies (family Hydropsychidae) are perhaps the most abundant and widespread caddisfly genera. The two genera are easily separable 2.2-63
LGS EROL except for very early instars. Each genus in the creeks contained multiple species. No key to larval Cheumatopsyche is available, but adults of at least three species (C. analis, C. sordida, C. campyla) were taken in a light trap collection at Spring Mount station.
Seven species of Hydropsyche occurred in the creeks, based largely upon the key to larvae by Ross (Ref 2.2-39) and determinations by the Applicant's consultant which were based mainly upon larval head capsule color patterns. Common species were A, C, and E. Species A larvae were the largest, and were found principally in the lower East Branch and Perkiomen Creek.
Species C was numerous in both creeks. Species E was restricted primarily to Sellersville and Cathill.
The larvae are omnivorous and can be found in almost every stream that is not severely polluted. They build loose stone retreats and capture nets where current speed is suitable for efficient food (seston) gathering. Both genera were commonly collected in drift samples, and exhibited an increase in density during darkness.
Although closely-related, the two genera exhibit differences in tolerance to organic enrichment and intermittent flow as evidenced by their contrasting spatial patterns in East Branch Perkiomen Creek. Cheumatopsyche was dominant at all stations in relatively high numbers, whereas Hydropsyche was abundant at most stations, but essentially absent from Elephant (discontinuous flow) and Sellersville and Cathill (degraded water quality). In East Branch Perkiomen Creek, Hydropsyche outnumbered Cheumatopsyche only at WaWa. In Perkiomen Creek, the annual mean standing crop of Cheumatopsyche was roughly twice that of Hydropsyche. Cheumatopsyche in this system clearly had the competitive advantage. Larvae of both genera were most abundant in summer and fall. Pupae were present from April through October.
2.2.2.6.3.19 Leucotrichia pictipes L. pictipes is an easily recognizable, fast-water micro-caddisfly intolerant of organic pollution. Its case adheres tightly to the upper surface of stones, and for this reason its numbers are certainly underestimated. It actively feeds on surrounding algae and associated detritus. It was essentially absent from the upper and middle East Branch Perkiomen Creek, dominant in the lower East Branch (Moyer and WaWa), and common but not dominant in Perkiomen Creek. Highest larval numbers occurred in late summer and fall.
2.2.2.2.6.3.20 Tipula spp.
2.2-64
LGS EROL This is the largest cranefly genus and several species were collected in the creeks. No key to the immatures is available.
The only commonly encountered species was quite large (up to 70 mm extended), and on this basis was provisionally called T.
abdominalis. It was collected most frequently in the upper East Branch. The preferred habitat is submerged vegetative matter in riffles, runs, or pools. They are detritivorous. Numerical densities were low and greatest in late fall and winter.
2.2.2.2.6.3.21 Simuliidae Two genera of blackfly larva were identified in the creeks, Prosimulium (rare) and Simulium (abundant). It is difficult to key larval Simulium to species, but on the basis of pupae S.
vittatum is the most common species in the creeks, and is also one of the most common species in the U.S. Blackfly larvae are found in the shallows of streams where current is swift, their cephalic fans screening passing water for food particles. Some species of Simulium are very tolerant of organic pollution and can become abundant in partially polluted streams.
Simuliidae was abundant in the creeks and was dominant at all stations. Larval standing crops were high throughout the year with peaks in May, September, and November. Pupae, also present in all months, were most numerous in May and June. Larvae were often abundant in drift, and exhibited a nocturnal periodicity.
2.2.2.2.6.3.22 Chironomidae The true midges were the most abundant and diverse group of invertebrates in the creeks, comprising at least 37 genera (Table 2.2-44). Midge larvae and pupae were abundant at all stations throughout the 4-year study period. Larvae often represented the highest percentage of total aquatic drift, but did not exhibit any periodicity at the family level.
Based upon intrafamily data collected in 1974, four midge taxa were dominant in the creeks; Cricotopus spp. (subfamily Orthocladiinae), Polypedilum spp. and Tanytarsini (subfamily Chironominae), and Pentaneurini (subfamily Tanypodinae). Larvae of the tribe Pentaneurini do not build cases and are predaceous; other insect larvae form a large portion of their diet. They were numerous in the upper East Branch, peaked in abundance at Cathill, and were much reduced in number farther downstream and in Perkiomen Creek.
Larvae of Tanytarsini (Micropsectra and Tanytarsus) were found at all stations in varying numbers, but were present in maximum densities at Spring Mount where near torrential flow and rubble substrate were evidently conducive to the support of large 2.2-65
LGS EROL populations. Larvae of stream species characteristically construct a fixed case, and net that strains food particles from the current.
Only two species of Polypedilum were found in the creeks, P.
fallax and P. illinoense. P. fallax was rare. The genus was found at all stations, but maximum numbers occurred in the lower East Branch in summer. Larvae construct flimsy tubes, and food is derived from seston caught on temporary nets extending across the lumen of the tube or from actively grazing sediment. Other important taxa in the tribe Chironomini were Chironomus spp.,
Dicrotendipes sp, Microtendipes tarsalis, and Stictochironomus sp Chironomini was not abundant in Perkiomen Creek.
Cricotopus spp. dominated the chironomid community at all stations but Elephant, and were most abundant at Spring Mount.
Several species of this genus were recognized, but only 2 could be identified with any degree of certainty, C. bicinctus and C.
sp. 1 (Roback, Ref 2.2-38). Roback (Ref 2.2-38) found C.
bicinctus to be the most common Cricotopus species i-n southeastern Pennsylvania. It has been collected from intermittent streams and is particularly resistent to organic enrichment, low dissolved oxygen concentration, and at least some heavy metals.
Most Orthocladiinae are either algal or algal-detrital feeders, and larvae probably seek out and ingest their food directly from the substrate on which they live. In general, the subfamily is more abundant in colder months. Cardiocladius obscurus was present in relatively high numbers at WaWa, Spring Mount, and Rahns. From field observation, Orthocladius rivulorum was at times present in large numbers at Spring Mount inhabiting flexible tubes attached at one end to substrate surfaces.
In 1974, chironomid diversity was highest at Elephant probably because this station displayed the most varied flow conditions that ranged from intermittent (static) to flood. The fewest taxa were collected at WaWa.
2.2.2.2.6.3.23 Physa acuta Physa snails collected from all stations on one date in 1977 were identified as P. acuta by William J. Clench (personal comment).
The Applicant's consultant has often observed this snail out of water on rocks near the air-water interface, although it probably cannot tolerate drying. Like most Physa species it is tolerant of organic enrichment, and by using atmospheric oxygen for respiration can exist in anaerobic waters for extended periods.
Physa is a scavenger and essentially omnivorous. The coating of living algae, which covers most submerged surfaces, forms its 2.2-66
LGS EROL chief food, but dead plant and animal material is frequently ingested.
P. acuta was collected from all stations in the study period, but was most numerous in the middle East Branch where, on some occasions, it was extremely abundant on all types of substrate.
It was present in all months, but reached maximum densities in late summer and fall.
2.2.2.2.6.3.24 Sphaerium spp.
At least two species of Sphaerium (fingernail clams) were found in the creeks, S. striatinum and S. rhomboideum. The former was common at Sellersville; the latter was abundant at WaWa. The family is considered to be tolerant of polluted conditions.
Sphaerium was collected year-round and was present in greatest density (due to high numbers of young) in late summer and fall.
Sphaerium spp. are sessile and utilize organic seston, filtered from the water brought in through the incurrent siphon, as a food source.
2.2.2.2.6.4 Drift Macroinvertebrate drift refers to the downstream transport of benthic macroinvertebrates in freshwater streams. Stream drift is utilized as a food source by many fishes, and may play an important role in the recolonization of depopulated areas and redistribution of benthos.
A pilot 24-hour drift study was conducted on Perkiomen Creek at Graterford in August 1972. Subsequent studies were conducted concurrently in the East Branch and Perkiomen creeks once a month during April through October 1973 and April through September 1974 (Tables 2.2-40 and 41 and 2.2-70 and 71). Study periods corresponded to the period when flow augmentation may be required during plant operation. Concurrent sampling allowed a comparative assessment of drift between creeks.
Aquatic drift densities in both creeks were variable over the study period, and ranged from 471 to 11,012 animals/1000 m3 in East Branch Perkiomen Creek and 321 to 11,492/1200 m3 in Perkiomen Creek (Table 2.2-51). Although mean monthly numerical drift densities averaged 48% greater in Perkiomen Creek in the 13-month study period, they were often similar to those recorded in the East Branch. Biomass (mg dry wt/1000m3 ) ranged from 22 to 453 and from 43 to 629 in East Branch and Perkiomen Creek, respectively. Monthly biomass densities were often similar between creeks, but averaged 14% greater in Perkiomen Creek.
Mean monthly drift densities, numbers and biomass, were significantly (P is less than, or equal to 0.10) correlated 2.2-67
LGS EROL W (Spearman's rank correlation coefficient) between streams. Total drift per unit of time was consistently greater in Perkiomen Creek due to greater velocity (2.0-3.7 times greater in Perkiomen Creek) and discharge.
Drift densities varied, sometimes markedly, from month to month in the same creek, and appeared to fluctuate in response to short-term phenomena which essentially precluded extrapolation of results to the entire month or even several days.
In all, 61 taxa were collected in drift samples from East Branch drift Creek Perkiomen When and 92 from Perkiomen Creek in the study period.
studies were combined by year within creek it was evident that chironomid larvae and pupae dominated drift numerically in both creeks (Table 2.2-51), followed by Baetis, Hydro2syche, and Cheumatopsyche. These organisms were also relatively abundant in most months. The Naididae was dominant in Perkiomen Creek, but was taken in high numbers only in May 1974.
More taxa were collected in Perkiomen Creek samples in all months. This reflected the greater benthic richness of Perkiomen Creek, and the higher velocities that resulted in the chance capture of more organisms uncommon in the drift over an equal sampling period.
. The aquatic component generally accounted for the greatest percentage of total drift; emergent drifters were next in numbers. Input from strictly terrestrial sources was the smallest, although certain insects were occasionally abundant.
Based upon monthly estimates in 1973 the proportion of benthos in the drift ranged from 0.0009 to 0.0099% in the East Branch and from 0.0020 to 0.1316% in Perkiomen Creek. Higher percentages would be expected at certain times in the life histories of individual populations. For example, a high proportion of pupal Cricotopus (midge) may be in the water column prior to eclosion.
Mean monthly densities of aquatic drifters per 1000 m3 in Perkiomen Creek were compared with benthic densities per m2 at Rahns (790 m downstream) in corresponding months. Although benthos, like drift, was dominated by Diptera and Trichoptera, there was no clear consistent proportional relationship between benthic standing crop and drift density. Note that benthic values were based upon riffle habitats, whereas drift organisms originated primarily from run habitats.
Sampling every 2 hours2.314815e-5 days <br />5.555556e-4 hours <br />3.306878e-6 weeks <br />7.61e-7 months <br /> provided data on diel periodicity of aquatic drift. Total densities varied markedly, but somewhat predictably over the 24-hour period. Maximum densities (numbers and biomass) in both creeks occurred after sunset since most drifters exhibited a nocturnal behavioral periodicity (Table 2.2-52), a phenomenon apparently unaffected by dissolved 2.2-68
LGS EROL oxygen concentration, water temperature, or velocity as measured in this study. This relationship between invertebrate drift and changes in light intensity has been well-documented (Waters, Ref 2.2-50).
Dominant drift organisms (Table 2.2-51) that did not display behavioral nocturnal drift were Chironomidae (no apparent periodicity) and Naididae (day-active). Chironomids as a group rarely exhibit a diel periodicity. This is not surprising since these insects are commonly diverse in lotic systems, and their treatment at the family level may obscure any discrete but overlapping periodicities that may otherwise be evident at the genus or species level. Chironomidae was the most diverse family in the study area, comprising at least 37 genera. The number of taxa that drifted was greatest during darkness (Table 2.2-52).
2.2.2.2.7 Fish The fish community of Perkiomen Creek was typical of those found in other lotic systems of similar size in southeastern Pennsylvania (Mihursky, Ref 2.2-77). In general, the fish fauna ranged from minnows, important as both primary consumers and forage for top-level carnivores, to the pike and sunfish families that are sociologically important for recreation, and ecologically significant as key predators. With few exceptions the species were indigenous and reproduced locally.
Historically, man has influenced the fish community of Perkiomen Creek by altering water quality, changing morphology and flow patterns with dams and reservoirs, and introducing or maintaining species by stocking. Operation of LGS may affect the existing fish community due to diversion and water withdrawal (entrainment and impingement). In order to evaluate these impacts, the fish community has been intensively sampled, primarily by seine and electrofishing, for 7 years (Tables 2.2-40 and 41).
2.2.2.2.7.1 Species Inventory A list of species collected from the creek from 1970 through 1977 is presented in Table 2.2-53. Qualitative abundance (defined in Section 2.2.2.1.7) was established by subjective comparison of recent catch statistics. In all, 8 families, including 40 species, were inventoried as well as hybrids of Esocidae, Cyprinidae, and within-genus Lepomis. This was a relatively large number of species considering the limited area sampled and the historic and geologic factors that have reduced the number of species in mid-Atlantic streams. None of the species in Perkiomen Creek is considered commercially valuable, 2.2-69
LGS EROL or rare, or endangered by either Federal or state regulatory agencies. The American eel is the only true migratory species.
The brook trout cannot maintain itself in Perkiomen Creek due to high water temperature, but has often been stocked in downstream tributaries by the Pennsylvania Fish Commission. Muskellunge was also stocked, although the capture of one young individual in 1977 indicated that limited natural reproduction had occurred.
2.2.2.2.7.2 Community Description 2.2.2.2.7.2.1 Larval Fish Larval fish drift in the area of the proposed Graterford intake (P14390) on Perkiomen Creek was investigated from 1973 through 1975. Larvae inhabiting the shoreline were studied using traps in 1975. Relative abundance of drifting larvae was similar between years (Table 2.2-54). Carp and minnows were first and second in abundance, respectively, while Lepomis spp. was usually third, and white sucker fourth. With the exception of carp, relative abundance of shoreline larvae was similar to that of drifting larvae; minnows were the most abundant, followed by white sucker and Lepomis spp. (Table 2.2-55).
The spawning seasons extend primarily from April through August.
Larval drift densities were low through April, peaked in late May or early June, peaked slightly again in early July or August, and decreased through September (Figure 2.2-16). These variations were caused by species-specific spawning periods (Table 2.2-56).
The perch family and white sucker spawned primarily in May. Two peak spawnings (early and mid-summer) occurred for both Notropis spp. and Lepomis spp. Spawning times varied somewhat between years due to environmental conditions.
Diel fluctuation in drift occurred regularly in Perkiomen Creek.
Most larvae were collected between sunset and sunrise, and peak densities usually occurred between 2200 and 0400 hours0.00463 days <br />0.111 hours <br />6.613757e-4 weeks <br />1.522e-4 months <br />.
A horizontal gradient in the abundance of drifting larvae was present in 1974 and 1975, with the highest densities usually occurring near shore. The horizontal distribution of individual taxa is discussed in following sections (Table 2.2-57). Total drift density did not vary between channels in 1975, although differences did occur for some taxa (Table 2.2-58).
2.2.2.2.7.2.2 Minnows and Young In 1975 and 1976, 29 species and Lepomis hybrids were collected by seine (Table 2.2-59). Most were minnows and young of larger species. The most abundant species (1975 and 1976 combined) were spotfin shiner (68% of total catch), spottail shiner (10%),
2.2-70
LGS EROL satinfin shiner (4%), comely shiner (3%), and white sucker (3%).
Each of the remaining species comprised less than 2% of the total catch. The relative abundance of dominant species varied-between 1975 and 1976. Minnows and young were generally more abundant in 1976 than in 1975. Within-year catches were highest in summer and fall months, reflecting the appearance of young-of-year fish (Table 2.2-61).
Redbreast sunfish and green sunfish dominated the electrofishing catch in 1975 and 1976; the relative abundance of young sunfish was similar between the years (Table 2.2-60).
The spotfin shiner was the most numerous species in each site in both years (Table 2.2-59). Relative abundances of other dominant species (spottail shiner, satinfin shiner, comely shiner, white sucker) varied little between sites. Total mean catch per net sweep was similar between sites. Relative abundance of young sunfish was significantly correlated between sites in both years.
The number of species captured per seine collection was used as an index of species diversity. Diversity was significantly greater in 1976 than in 1975, and significantly greater in summer and fall than in winter and spring due to the appearance of young-of-year fish during the former period (Table 2.2-61).
Spatial variability in diversity was due primarily to a signficantly greater number of species at P13580.
2.2.2.2.7.2.3 Adults In all, 21 species of large fish were collected by electrofishing in 1974, 1975, and 1976 (Table 2.2-62). Esocid, Cyprinid, and Lepomis hybrids were also captured. Large fish populations were relatively stable in Perkiomen Creek, as the total catch was similar at the same site between years, and catch of the 16 most abundant species was significantly correlated between years and between sites. The redbreast sunfish was the dominant species at all sites in all years, comprising 49% of the total catch. White sucker (12%) and smallmouth bass (11%) were the next most abundant species, followed by pumpkinseed, carp, green sunfish, and rock bass (each about 5% of total).
2.2.2.2.7.3 Important Species General criteria governing the designation of important species were given in Section 2.2. Important fishes selected for Perkiomen Creek, together with applicable criteria, are presented in Table 2.2-63. Generally, this diverse group includes the more sensitive fish of direct use to man, and species important to the structure and function of the ecosystem. Those chosen are also 2.2-71
LGS EROL
-N likely to be affected by the operation of the Graterford intake.
The local biology of important species is described below.
2.2.2.2.7.2.3.1 American Shad The American shad (Alosa sapidissima) was not found in Perkiomen Creek, and its introduction is dependent on the results of the Pennsylvania Fish Commission's program to provide fish passage-ways at dams downstream of LGS, on the Schuylkill River.
2.2.2.2.7.2.3.2 Muskellunge Young muskellunge (Esox masquinongy) and its sterile hybrid with the northern pike (Esox lucius) were uncommon in Perkiomen Creek.
Only three individuals were taken in three annual electrofishing surveys at four sites (Table 2.2-62). Monthly electrofishing yielded four in 1977. No muskellunge young were taken by seine in monthly sampling in 1975 and 1976; however, 1 small (30 mm FL) individual captured in May 1977 indicated that limited natural reproduction had occurred in the creek. Adults were also uncommon. One immature adult was captured in 1976, and 1 large
. (330 mm FL) individual was captured on 3 separate occasions in 1977. Muskellunge populations have apparently been primarily maintained by Pennsylvania Fish Commission stocking.
2.2.2.2.7.2.3.3 Carp Spawning of carp (Cyprinus carpio) in Perkiomen Creek took place in May of 1974 and 1975 at temperatures of 18 to 240C. The abundance of drifting carp larvae varied somewhat between 1973, 1974, and 1975, although it was always the most abundant species3 (Table 2.2-54). Mean drift densities were 0.1126 individuals/m (50% of total drift) in 1973, 0.4328 individuals/m 3 (80%) in 1974, and 0.1269 individuals/m 3 (46%) in 1975. The carp ranked fifth in abundance of trap catches of shoreline larvae (Table 2.2-55). Maximum drift densities shifted from July in 1973 to May in 1974 and 1975 (Table 2.2-56 and Figure 2.2-17).
Carp frequently drifted during the day in May, but were always more numerous at night. Carp were generally more abundant in drift near midstream than near shore (Table 2.2-57). Post-larvae and juveniles inhabited sheltered areas of quiet water.
Numerically, carp comprised a relatively small percentage of the
- electrofishing catch in all years (1974-1976) at all sites (Table 2.2-62). Adult carp ranged from 1% of total catch at P14160 in 1975 to 9% at P20000 in 1976. Differences in relative B abundance were slight at the same site between years. Carp were more abundant upstream of the intake site at P20000 (131 fish/ha) 2.2-72
LGS EROL and P14390 (67 fish/ha), due primarily to the abundance of their preferred habitats, (Table 2.2-65).
Carp were an important contributor to biomass at all sites, and dominated at P14390 in 1974 and 1976. They ranked second at other sites where their abundance was estimated. Biomass estimates varied both temporally and spatially in the same manner as numerical estimates. The longest carp collected in Perkiomen Creek measured 680 mm FL. A recreational fishery for carp exists on Perkiomen Creek because of the fish's size and fighting ability.
2.2.2.2.7.2.3.4 Comely Shiner In late July 1975 and 1976, young comely shiner (Notropis amoenus) appeared in seine catches from quiet, sheltered backwater areas downstream of runs and riffles. They ranked fourth in overall abundance in Perkiomen Creek seine catches (Table 2.2-59), and their temporal and spatial variations were not significant. Total mean catch per net sweep increased slightly from 6.2 in 1975 to 6.7 in 1976.
The longest comely shiner collected was 85 mm FL. The length-weight relationship was significantly different between 1975 and 1976, and between sites. Fish were heavier in 1975 than in 1976 (Table 2.2-67). Fish gained proportionately more weight per unit increase in length the farther upstream they were found.
2.2.2.2.7.2.3.5 Spottail Shiner Spawning of this species (Notropis hudsonius) in Perkiomen Creek occurred from May through June in 1974 and 1975. Larvae were identified in drift. The spottail shiner ranked second in overall abundance in seine catches (Table 2.2-59). Adults were most often collected in slow-moving water over gravel shoals.
Total mean catch per net sweep was significantly greater in 1976 (37.6) than in 1975 (2.9), and catches were highest in early summer when young appeared (Table 2.2-61). Distribution of individuals was more clumped in winter, but spatial variation of catch between sites was not significant.
The maximum length of fish caught was 97 mm FL. The spottail shiner length-weight relationship was significantly different between years and among sites. Increase in weight with length was greater in 1975 than in 1976 (Table 2.2-65). Faster growth in 1975 may have been due to reduced competition within the smaller population.
2.2-73
LGS EROL W 2.2.2.2.7.2.3.6 Spotfin Shiner Refer to Section 2.2.2.1.7 for information on feeding habits of spotfin shiner (Notropis spilopterus). Based upon larval collections, spotfin shiner spawned in mid-August of 1974, and in July through August of 1975, at temperatures between 26 and 290 C. It was the dominant species taken by seine and comprised 67%
of the combined total catch for 1975 and 1976 (Table 2.2-59). It appeared to have stable populations in Perkiomen Creek with no significant variation between years or sites. The total mean catch of spotfin shiner per net sweep was, however, significantly higher in late summer and fall than at other times (Table 2.2-61). Length-weight relationships were similar between years but significantly different between sites (Table 2.2-67).
2.2.2.2.7.2.3.7 White Sucker Refer to Section 2.2.2.1.7 for information on feeding habits, diseases and the human importance of the white sucker.
(Catostomus commersoni). White suckers spawned early, since drifting larvae were collected only in May (Table 2.2-56).
Larvae frequently drifted during the day, but were always more
. numerous at night. Densities of drifting larvae were similar between 1973 and 1975, but were somewhat lower in 1974 (Table 2.2-54). The white sucker usually ranked fourth in abundance, and ranged from 1% of catch in 1974 to 7% in 1975. It ranked second in abundance (8%) in shoreline trap catches in 1975 (Table 2.2-55). In 1975, drifting larvae at P14390 were more abundant in the east, rather than the west, channel (Table 2.2-58).
Seine catch of young white suckers increased from 0.1 per unit effort in 1975 to 12.5 in 1976 (Table 2.2-59). Largest catches occurred at the extreme upstream and downstream seine sites in 1976.
The white sucker was the second most abundant large fish in Perkiomen Creek (Table 2.2-62). Differences in abundance between years was variable depending on the site. Estimates at P14390 were not statistically different between 1974 and 1976, but estimates were higher in 1976 than in 1974 at P14020 and P14160 (Table 2.2-65). Spatial variation was also inconsistent. All three sites in 1974 had similar estimates of abundance. In 1976, abundance was less at P14390 and P14020 (139 and 258 fish/ha, respectively) than at P20000 and P14160 (314 and 334 fish/ha).
The white sucker was the most important contributor to biomass at all sites except P14390, where it was exceeded by carp. Spatial and temporal trends were similar for biomass and number estimates. Most growth ocpurred in the first year of life (Table 2.2-68). White suckers at P14020 were significantly 2.2-74
LGS EROL smaller at age II than individuals at other sites. No general trend in growth patterns was evident for the length of white suckers studied in the area of Perkiomen Creek. A significant difference in length-weight regression coefficients existed between four sites in 1976. Fish gained proportionately more weight per unit increase in length the further downstream they were found (Table 2.2-69).
2.2.2.2.7.2.3.8 Redbreast Sunfish Refer to Section 2.2.2.1.7 for information on food habits and diseases of the redbreast sunfish (Lepomis auritus). Larvae grouped as Lepomis spp. were usually third in overall drift abundance (Table 2.2-54). The majority were probably redbreast sunfish because this species is the dominant adult in Perkiomen Creek, and most larval sunfish collected in 1975 were identified as belonging to this species. Lepomis spp. comprised a consistent percentage of drift catch from 1973 to 1975 (4-8%).
Composition of trap samples of shoreline larvae was similar (Table 2.2-55). Peak drift densities of Lepomis occurred in July 1973, mid-June 1974, and early July 1975 (Table 2.2-56 Figure 2.2-17). Larval sunfish were generally most abundant in samples taken closer to shore in 1975 (Table 2.2-57).
Redbreast sunfish young ranked eighth in overall abundance in the seine catch. Annual variation in abundance was not great; mean catch per net sweep increased in numbers from 1.6 (1% of total catch) in 1975 to 3.1 (1% of total catch) in 1976 (Table 2.2-59).
Electrofishing estimates of redbreast sunfish abundance exhibited a similar trend (Table 2.2-64). Spatial variation in abundance between the six seine sites was slight and usually ranged between 1 and 2%. Electrofishing estimates varied from 24 fish per 20 m of shoreline at P14225 to 75 fish per 20 m of shoreline at P14690 in 1976.
The redbreast sunfish was consistently the most abundant large fish in Perkiomen Creek (Table 2.2-62). It ranged from 36% of total catch at P20000 to 61% at P14160 in 1976. Annual variation for the total population was slight. Although estimates of age I were significantly lower in 1976 compared to 1974 at most sites, estimates of older age groups were always similar (Table 2.2-66).
Estimates by age group revealed that 1975 was a relatively weak year-class compared to 1973. Spatial variation in the number of fish per hectare was great (Table 2.2-65). Site P14160 had the greatest density of redbreast sunfish in both years (1622/ha in 1974, 1397/ha in 1976) followed by P14020 (897/ha'in 1974, 511/ha in 1976), P20000 (415/ha in 1976), and P14390 (437/ha in 1974, 338/ha in 1976).
Maximum age in 1973 was V (Table 2.2-68). Greatest growth in length occurred in the second year. In 1976, temporal and 2.2-75
LGS EROL spatial variations in length at annulus were evident. Fish were generally smaller at each annulus at P20000, larger at P14390, and approximately equal at P14020 and P14160.
2.2.2.2.7.2.3.9 Smallmouth Bass Smallmouth bass (Micropterus dolomieui) larvae (unlike juveniles) rarely occurred in Perkiomen Creek drift. Young bass were relatively low in abundance (1% of total seine catch), although they comprised the second most abundant member of the sunfish family (Table 2.2-59). Abundance varied annually, increasing in numbers from 0.4 fish per net sweep in 1975 (<1% of total catch) to 3.8 (1%) in 1976. This species was more abundant at P14320, P16500, and P19775 where it accounted for roughly 2% of the total catch. At other sites it averaged 1% of the total catch.
The smallmouth bass was the third most abundant large fish (11%
of total) based upon 3 years of electrofishing in Perkiomen Creek (Table 2.2-62). Relative abundance remained constant within site between years. Population estimates were similar between 1975 and 1976 at P14160, but different between 1974 and 1976 at P14390 (Table 2.2-65). Estimates of abundance were larger at downstream sites. In 1976, site P14160 contained 163 fish per ha compared to 84 fish per ha at P14390.
Smallmouth bass ranked fourth in biomass at sites where abundance of all important species could be estimated. Their biomass was greatest at sites where numerical abundance was greatest. Bass appeared to weigh less in 1975 than 1976, due to the smaller size structure of the population. Individuals ranged up to 469 mm FL.
An age and growth study in 1973 revealed that the oldest specimen was age III (Table 2.2-68). Most growth (39% of total) occurred in the first year of life. The 1970 year-class exhibited the highest growth rate. Significant spatial variation occurred for fish length at each annulus. Age structure indicated dominant age-groups I and II and a weak age-group III. Smallmouth bass was actively sought by fishermen in Perkiomen Creek.
2.2.2.2.7.2.3.10 Shield Darter Peak spawning of shield darters (Percina peltata) occurred in May (Table 2.2-55). Larval catches were consistently low in drift and trap samples (Tables 2.2-54 and 55). Number per m3 ranged from 0.2% of total in 1974 to 1.0% in 1973 and 1975. Shield darters drifted during the day, but were more numerous at night.
Spatial distribution across the stream was fairly consistent in 1975 (Table 2.2-57). Shield darters comprised <1% of the total catch in 1975 and 1976 (Table 2.2-59). Total mean catch per net sweep showed little temporal or spatial variation.
2.2-76
LGS EROL 2.2.2.2.8 Trophic Relationships Refer to Section 2.2.2.1.8.
2.2.2.3 East Branch Perkiomen Creek East Branch Perkiomen Creek is a warm water stream that drains 158 km2 of the Piedmont physiographic province in southeastern Pennsylvania. It flows southwest approximately 39 km from its source in Bedminster Township to its confluence with Perkiomen Creek just below Schwenksville, Pennsylvania (Figure 2.2-15).
The creek has a low gradient (1.9 m/km) and consists of riffle and run habitats with few natural pools. Several small man-made impoundments are located in the lower half. The stream supports diverse and productive flora and fauna.
Because the entire creek will be used for diversion, the East Branch Perkiomen Creek study area includes the creek from just above Elephant Road bridge downstream to the confluence with.
Perkiomen Creek. For a further description of this area, refer to Section 6.1. Sample stations are designated by common names, and by the letter 'E' followed by a number that indicates the distance in meters from the mouth of the creek. Where stations include several meters of stream, site numbers designate the downstream end of the station.
The biota of East Branch Perkiomen Creek was extensively stufied by the Applicant's consultant from 1970 through 1978. A sampling history by program is given in Tables 2.2-70 and 71.
2.2.2.3.1 Water Quality and Environmental Stress East Branch Perkiomen Creek is a major tributary to Perkiomen Creek. Much of the watershed is used for agriculture, but land is increasingly being developed for residential use. The major population concentration occurs midway on the creek at Sellersville-Perkasie.
Low natural base flows and frequent localized storms produce an extremely variable flow regime. Spring flows are generally high due to snow melt and precipitation, and spates occur throughout the year. As summer approaches, flows become lower, and in late summer and fall surface flow in upper reaches often ceases.
Riffle habitat is much reduced or eliminated in about one-third of the stream length, and the creek becomes a series of pools or quiescent reaches connected by subsurface percolation. Several low dams are present.
2.2-77
LGS EROL W Anthropogenic stresses from nonpoint source runoff is a problem, particularly in the headwaters where most of the surrounding land is used for agriculture. Runoff from farmland carries a heavy load of nutrients. Stormwater and sewage enter the East Branch via storm drains under the Route 309 bridge in Sellersville.
This enriched discharge is most persistent during periods of heavy rainfall when the Sellersville-Perkasie Sewage Treatment Plant capacity is exceeded.
The greatest point source stress is the Sellersville-Perkasie Sewage Treatment Plant (secondary treatment) effluent that enters the creek about 3 km upstream of Cathill Road (E23000, about midpoint on the creek). The effluent contains very high levels of chlorine, nutrients, and heavy metals (Table 2.4-9). Residual chlorine has its greatest effect in the immediate vicinity of the outfall. Chlorine rapidly diffuses into the atmosphere and decays as a result of photochemical reactions. However, since the effluent is highly enriched with nitrogenous compounds, chloramines are formed as a result of chlorination and these may persist in the stream. The stimulating effect of nutrients on aquatic plant growth can produce marked diel fluctuations in dissolved oxygen (DO). Several 24-hour DO studies conducted by the Applicant's consultant showed that a critical DO depression
. (<2mg/l; the Commonwealth's minimum criterion is 4.0) and extreme.
diel fluctuation occurred downstream of the effluent.
metals such as cadmium, chromium, copper, and zinc are Heavy concentrated in the effluent. All the factors described above produce a stressed community downstream of the outfall.
Indian Creek (which enters the East Branch near meter 6900) may also stress the East Branch. It receives effluents from the Telford Borough and Lower Salford Township Sewage Treatment Plants, and a number of food-processing industries. The primary stress created by Indian Creek is nutrient loading, and it appears that this creek may periodically degrade lower East Branch water quality.
2.2.2.3.2 Phytoplankton Phytoplankton was not studied by the Applicant's consultant in East Branch Perkiomen Creek because it was considered to be of low potential impact. Studies conducted in other shallow, temperate headwater streams have indicated that phytoplankton is typically low in density and essentially of periphytic origin.
2.2-78
LGS EROL 2.2.2.3.3 Periphyton Periphyton is a seasonally important primary producer in East Branch Perkiomen Creek and was studied by the Applicant's consultant in 1973 and 1974 as shown in Tables 2.2-70 and 71.
Periphytic algae were almost exclusively diatoms and only the common genera were recorded. These were Navicula, Melosira, Synedra, Nitzschia, and Cocconeis. Local biology and habitat requirements for these algae have already been described, and seasonal changes in the taxonomic composition of periphyton were similar to those observed in the Schuylkill River (Section 2.2.2.1.3).
Periphyton standing crop biomass in the East Branch was highly variable, and apparently responsive to a number of environmental factors. Biomass was maximum in April through October under conditions of relatively stable low flow and high temperature (Table 2.2-72). Highest biomass occurred in August of both years (1973, 48 mg/dm2 ; 1974, 106 mg/dM2 ). Biomass was low from January through March and from November through December, due to increased velocities and lower temperatures. This seasonal pattern of periphyton productivity is typical of lotic systems in temperate regions.
Periphyton in the upper East Branch (E32115, E22867) was more susceptible to scouring during increased flow than periphyton in the lower section (E2800). During periods of low flow E32115 and E22867 exhibited higher periphyton biomass than E2800, probably because the shallower water allowed more light to reach the per iphyton community.
2.2.2.3.4 Macrophytes Refer to Section 2.2.2.2.4.
2.2.2.3.5 Zooplankton Refer to Section 2.2.2.2.5.
2.2.2.3.6 Macroinvertebrates Refer to Section 2.2.2.2.6.
2.2-79
LGS EROL W 2.2.2.3.7 Fish The fish community of East Branch Perkiomen Creek consists of warmwater species typical of small lotic systems in southeastern Pennsylvania (Mihursky, Ref 2.2-77). In general, the fish include minnows and suckers, important as food convertors and forage; and freshwater catfish, pike, and sunfish, important ecologically at higher trophic levels and sociologically as pan and sport fish. Most species are indigenous and reproduce locally.
To some extent fish distribution in the East Branch reflected longitudinal zonation typical of lotic systems. However, characteristic distributions were modif-ied somewhat by major point source domestic and industrial discharge (Section 2.2.2.3.1) and the presence of several small impoundments.
Operation of LGS will require the diversion of Delaware River water through the East Branch. Fish in the creek will be affected directly-by the increased discharge, and indirectly by habitat alteration.
The entire East Branch was intensively sampled at least monthly,
- from June 1970 through December 1976 (Tables 2.2-70 and 71).
Fishes were captured primarily by seine and electrofishing.
2.2.2'3.7.1 Species Inventory In all, 9 families, including 23 genera and 40 species, were collected (Table 2.2-73), as well as hybrids of both the minnow and carp family and the genus Lepomis. No species were commercially valuable, or considered threatened or endangered by Federal or state regulatory agencies. The American eel was the only true migratory (catadromous) species.
Qualitative abundance was established within a family, or among related families, by subjective comparison of recent catch statistics (Section 2.2.2.1.7). Species designated rare or uncommon were low in abundance, and significant alteration of their environment could result in a change in distribution or possible extirpation. Brook trout, a coldwater fish, was occasionally stocked in the creek by the Pennsylvania Fish Commission, but did not sustain itself. A single muskellunge captured near the mouth of the creek was assumed to have originated from Perkiomen Creek, where muskellunge have been stocked.
2.2-80
LGS EROL 2.2.2.3.7.2 Community Description 2.2.2.3.7.2.1 Larval Fish Larval fish drift at E2650 was investigated in 1973 and 1974 using drift nets. Data collected from this site were representative only of the lower East Branch. Relative abundance of dominant taxa (comprising >90% of the total identified catch) varied between years (Table 2.2-74). In 1973, the white sucker and yellow bullhead were first and third in abundance, respectively, whereas Lepomis spp. were first, and white sucker third, in 1974. Unidentified minnows (mostly Notropis spp.)
ranked second in both years.
Spawning extended primarily from May through August. Density of drifting larvae varied during this period (Figure 2.2-18) as a result of species-specific peak spawns (Table 2.2-75). White suckers and tessellated darters spawned primarily from late April to early May, while yellow bullheads spawned in early June. Two peak spawning periods for both Notropis spp. and Lepomis spp.
were observed; one in early June, and one from July to early August. Few (22) drifting eggs were taken because most East Branch fishes spawn demersal eggs.
Diel fluctuation in drift occurred regularly. Most larvae were collected between sunset and sunrise; peak densities usually occurred between 2200 and 0200 hours0.00231 days <br />0.0556 hours <br />3.306878e-4 weeks <br />7.61e-5 months <br />.
2.2.2.3.7.2.2 Minnows and Young In 1975 and 1976, 30 species and Lepomis and Notropis hybrids were collected by seine from lotic sites in East Branch Perkiomen Creek (Table 2.2-76). Most were minnows and young-of-year pan and sport fishes. The few adult pan and sport fishes that were included did not affect results.
Total abundance of minnows and young (mean catch-per-unit-effort) did not differ between years. Dominant species, based upon in 1975 and 1976 combined seine data, were the spotfin shiner (54%
of total), bluntnose minnow, banded killifish, tessellated darter (each 6%), and common shiner (5%). All other species individually comprised less than 5% of the mean catch-per-unit-effort. Relative abundance of the more numerous species varied between 1975 and 1976. In 1975, spotfin shiner, comely shiner, swallowtail shiner, common shiner, and satinfin shiner dominated the catch, while in 1976, spotfin shiner, tessellated darter, banded killifish, bluntnose minnow, and white sucker (young) were most numerous.
2.2-81
LGS EROL The spotfin shiner was the most numerous species in each site, and abundance of dominant species varied between sites.
Variation in spatial relative abundance was indicative of species, zonation. Bridle shiner, common shiner, spottail shiner, swallowtail shiner, spotf in shiner, bluntnose minnow, creek chubsucker, and Lepomis hybrid were common in the upstream section of the East Branch; goldfish, golden shiner, and creek chub were established primarily in the middle reaches; and carp, cutlips minnow, satinfin shiner, longnose dace, fallfish, and margined madtom were more prevalent downstream. Other species were generally distributed throughout the creek. Other investigators have demonstrated similar patterns of longitudinal zonation in small streams (Burton and Odum, Ref 2.2-78; Larimore and Smith, Ref 2.2-79; and Hocutt and Stauffer, Ref 2.2-80).
Species segregation occurred as a result of longitudinal changes in habitat and water quality.
The number of species per collection was used as a general index of diversity. This parameter also indicated a pattern of longitudinal zonation in the creek. Number of species increased from headwaters to about midpoint in the stream, then decreased.
downstream toward the confluence. Usually, the number of species increases downstream as a result of increased habitat heterogeneity (Larimore and Smith, Ref 2.2-79). Lower diversity in the downstream reaches of the East Branch may have reflected degraded water quality downstream of Sellersville, and sampling method bias toward smaller (i.e., upstream) stream size.
2.2.2.3.7.2.3 Adults 2.2.2.3.7.2.3.1 Lotic Sites In all, 18 species of large fish (defined as all members larger than 50 mm FL of the pike, sucker, freshwater catfish, and sunfish families, and goldfish and carp) were collected from lotic sites by dc electrofishing in 1973 and 1975. Goldfish x carp and Lepomis hybirds also were collected. White sucker, green sunfish, yellow bullhead, and redbreast sunfish dominated in both years (Table 2.2-77), and comprised 25, 23 19, and 15%,
respectively, of the total estimated streamwide number.
Relative abundance of the 14 most abundant species remained essentially the same between 1973 and 1975 at each site, but often varied between sites in each year. The four dominant species were generally important throughout the stream and comprised from 50 to 91% of the large fish community at each site. Pumpkinseed and Lepomis hybrid were only 4 and 3% of total, respectively, but were important at E36020. Other locally important species were redfin pickerel (E36020), bluegill (E30540), and smallmouth bass and margined madtom (E1550).
2.2-82
LGS EROL Species zonation was likely due to habitat variety and water quality differences, as mentioned previously.
Results of biomass analyses were very similar to those based upon population estimates. White sucker (46% of total estimated biomass), yellow bullhead (13%), carp (11%), redbreast sunfish (9%), and green sunfish (8%) comprised most of the of biomass.
No other species accounted for more than 5% of the total, but the following fishes made significant contributions at specific locations and times: pumpkinseed (E36020, 1975), Lepomis hybrid (E36020, both years), creek chubsucker (E36020, 1973), redfin pickerel (E36020, 1975), chain pickerel (E36020, 1975), brown bullhead (E22240,1975), and smallmouth bass (E1550, 1975).
2.2.2.3.7.2.3.2 Lentic Sites In all, 16 species and carp x goldfish and Lepomis hybrids were collected in spring 1974 and fall 1975 at Fretz (E15500) and WaWa (E5650) reservoirs (Table 2.2-78). Percent composition of total catch was used to evaluate community structure, because unbiased population estimates could not be calculated for each species.
The green sunfish was the most abundant species in both reservoirs in 1974 and 1975. White sucker, pumpkinseed, and yellow bullhead followed green sunfish in order of overall abundance at the two sites. The bluegill and pumpkinseed were more numerous in Fretz than WAWa, probably because of habitat differences. The yellow bullhead was relatively more abundant in WaWa where, during low flows, the site was more characteristic of lotic habitat. The brown bullhead was more common in Fretz, which was typically lentic.
Studies of fishes in the East Branch identified the presence of large numbers of hybrid sunfish (offspring of interspecific matings within the genus Lepomis), particularly in the headwaters (Tables 2.2-76 and 77). Hybrid sunfish ranked sixth among large fish in streamwide abundance, and ninth in streamwide biomass for 1973 and 1975 combined (Table 2.2-77). Hybrids often comprised more than 25% of the total sunfish population in headwater sites (more than 40% at E36020). Abundance declined somewhat steadily downstream where they were 5 to 10% of total.
The high incidence of hybrid sunfish in the East Branch was unusual. Hybrids commonly occur in habitat suitable for compatible sunfishes; however they commonly comprise only a very small percentage of the total sunfish population (Bailey and Lagler, Ref 2.2-81; and Birdsong and Yerger, Ref 2.2-82).
Hybrids were rare or nonexistant in several sites on nearby Tohickon and Neshaminy Creeks, which have habitats similar to those in the upper East Branch. Hybrids were also uncommon in the Schuylkill River and Perkiomen Creek study areas.
Hybridization in the East Branch was most likely due to crowding 2.2-83
LGS EROL in isolated pools during the spawning season when flow in the upstream reaches was often intermittent (Section 2.2.2.3.1).
2.2.2.3.7.3 Important Species General criteria for designation of important species were given in Section 2.2. A relatively large number of species were selected because effects of diversion on fishes of East Branch Perkiomen Creek are expected to be diverse and spatially variable due to the variety of habitats and the presence of existing stresses (Section 2.2.2.3.1). Important species were chosen to represent three general ecological niches present in the creek, and taxa of sociological importance (Table 2.2-79). These fishes will also most likely be affected by changes in the physical and chemical nature of the creek caused by diversion. The local biology of important species is described below.
2.2.2.3.7.3.1 Redfin Pickerel The redfin pickerel (Esox americanus) was common only in the headwaters, often being found in isolated shallow pools with no flow and heavy aquatic vegetation. The species was most numerous at E36020 (62 individuals/500 m of stream), and showed a decreasing trend in abundance downstream (Table 2.2-80). Only one specimen was taken from the two impoundments sampled (Table 2.2-81). Populations increased dramatically from 1973 to 1975, especially at E36020, where numbers almost doubled.
Variations in biomass were similar to those in abundance.
The maximum age was 4-5 years, but most specimens were age I (Table 2.2-84). Maximum length was 309 mm FL. Greatest (48%)
growth in length occurred in the first year of life. The length-weight relationship of 32 specimens was In W = -10.17 +
2.67 in FL. Although this species is a common game fish, angling for redfin pickerel in the East Branch was virtually nonexistent because of small adult size.
2.2.2.3.7.3.2 Satinfin Shiner The satinfin shiner (Notropis analostanus) was common in East Branch Perkiomen Creek, preferring habitat with fast current and bedrock substrate. Streamwide abundance based upon seine collections decreased from a mean catch-per-unit-effort of 13.4 in 1975 to 8.1 in 1976, and it ranked seventh in overall abundance (Table 2.2-76). This species was most important in downstream reaches at E1890, E5475, and E12440.
2.2-84
LGS EROL 2.2.2.3.7.3.3 Common Shiner Common shiners (Notropis cornutus) spawned from June through July. The occurrence of two peak larval drift periods, one each in June and July, may have indicated intermittent or multiple spawning (Table 2.2-75). Mean daily larval drift density in 1974 ranged from 0.007 larvae/m3 in mid-June to 0.012 larvae/m3 in late July. Common shiners ranked third in overall seine catch (Table 2.2-76). Mean catch-per-unit-effort increased from 14.8 in 1975 to 18.2 in 1976. Variation in abundance between sites was significant. This fish was more prevalent in upstream reaches at E32170 and E29810. Abundance was lowest at E22980, probably due to degraded water quality downstream of Sellersville (Section 2.2.2.3.1). Length-weight relationships of the common shiner differed significantly between 1975 and 197.6, as well as between sites (Table 2.2-82). Individuals at E29810 grew slower in weight per unit length relative to other sites.
2.2.2.3.7.3.4 Spotfin Shiner Larval drift densities of spotfin shiner (Notropis spilopterus) in the East Branch were highest in July and August in 1974. This species ranked first in overall seine catch (Table 2.2-76). Mean catch-per-unit-effort decreased from 234.2 in 1975 to 110.8 in 1976. Variation between sites was significant, the species being more prevalent in upstream reaches at E29810 and E32170.
Abundance did not decrease sharply downstream of Sellersville, indicating that this species was tolerant of degraded water quality (Section 2.2.2.3.1). Length-weight relationships varied significantly between 1975 and 1976 as well as between sites (Table 2.2-82). The high regression coefficients at E12440 and E22980 (downstream of, and in Sellersville, respectively) was again indicative of this species' tolerance of poor water quality.
2.2.2.3.7.3.5 White Sucker Refer to Section 2.2.2.1.7 for information on food habits and parasites and diseases of white sucker (Catostomus commersoni).
The white sucker generally spawned in May in 1973 and 1974 (earlier than most important species in the East Branch) and had a relatively short spawning period. Abundance of larvae in drift varied between 1973 and 1974 (Table 2.2-74). In 1973, white sucker mean drift density was 0.1234 individuals/m3 (60% of total drift), but in 1974 declined to 0.1032 (26%). Maximum drift densities occurred in early May in both 1973 and 1974, and declined to negligible levels by early June (Table 2.2-75).
White suckers always drifted at a greater rate during the night, reaching peak densities between 2200 and 0400 hours0.00463 days <br />0.111 hours <br />6.613757e-4 weeks <br />1.522e-4 months <br />.
2.2-85
LGS EROL Now White sucker young in the seine catch ranked fifth in overall abundance (Table 2.2-76). Variation in abundance between 1975 and 1976 was high, with mean catch-per-unit-effort increasing from 3.7 in 1975 to 20.0 in 1976. Variation was high between upstream seine sites, but comparatively low between downstream sites. The white sucker dominated at E29810 and E1890.
Abundance of young was low at sites near Sellersville, but increased from E12440 downstream to E1890.
The white sucker was the most abundant adult fish collected by electrofishing (Table 2.2-80). Streamwide abundance decreased from a mean of 605 individuals/500 m in 1973 to 525 in 1975.
Abundance was lowest in upstream and downstream reaches, and peaked just downstream of Sellersville. While the area downstream of Sellersville was not prime spawning or nursery habitat, adults apparently moved into the region to benefit indirectly from the organic enrichment there (Section 2.2.2.3.1).
The white sucker was the most important contributor to streamwide biomass (mean, 47 kg/500 m), and it dominated every site.
Streamwide biomass increased from 1973 to 1975, even though numerical abundance declined. This is not an unusual short-term trend for a relatively long-lived species.
- Estimated abundance of adult white suckers in Fretz reservoir (E15500) decreased from 1149 to 576 specimens from May 1974 to October 1975, while population levels in WaWa (E5650) during the same period remained essentially stable (Table 2.2-81). This species was slightly more numerous in Fretz than WaWa. Biomass, however, was somewhat higher in WaWa in 1975.
White suckers collected upstream and downstream of Sellersville exhibited fairly stable growth in length from 1968 to 1973 (Table 2.2-85). No significant difference in growth for combined stations upstream and downstream of Sellersville was observed, but fish collected downstream were consistently larger at each annulus for all year-classes than upstream. Specimens were not aged past their fourth year because of scale inconsistencies.
Maximum length at capture was 344 mm FL.
Analysis of covariance indicated significantly different length-weight regressions among populations of white sucker collected at five sites in 1973 (Table 2.2-83). Generally, individuals upstream of Sellersville gained proportionately more weight per unit increase in length than those downstream.
2.2.2.3.7.3.6 Yellow Bullhead
. Yellow bullheads (Ictalurus natalis) spawned in June and July in 1973 and June in 1974. Because of nesting behavior and parental care, yellow bullhead larvae rarely occurred in drift. In 1973, 2.2-86
LGS EROL mean drift density was 0.0184 individuals/mr (9% of total drift),
but declined to 0.0090 individuals/m3 (2%) in 1974 (Table 2.2-74). Peak densities occurred in late June of 1973 and 1974 (Table 2.2-75). 'This species always drifted at a greater rate during the night, reaching peak densities between 2200 and 0200 hours0.00231 days <br />0.0556 hours <br />3.306878e-4 weeks <br />7.61e-5 months <br />.
Yellow bullhead young were not abundant in the seine catch and comprised less than 1% of the mean catch-per-unit-effort in 1975 and 1976 (Table 2.2-76) Young were more prevalent upstream of Sellersville, but generally comprised less than 1% of total mean catch in this area.
The yellow bullhead was the third most abundant adult fish collected by electrofishing (Table 2.2-80). Streamwide abundance increased from a mean of 317 individuals/500 m in 1973 to 563 in 1975. The adults were generally more numerous downstream of Sellersville. The apparent contradiction between these and seine results was likely due to the fact that the seine is not an effective gear for sampling young in larger downstream areas.
Yellow bullhead adults were also the third most important contributors to streamwide biomass, with a mean of 12 kg/500 m (Table 2.2-80). Generally, annual and site variation in this parameter was similar to that of estimated abundance. However, biomass was much higher at E1550, where abundance was lower, indicating that many of these fish were larger and older. This may have been a reason for the decline in abundance noted at E1550 from 1973 to 1975.
Abundance of adults increased in both Fretz and WaWa reservoirs from May 1974 to October 1975 (Table 2.2-81). This was likely the result of successful spawns in 1973 and 1974, because abundance varied similarly in lotic regions during the same general period. Both abundance and biomass were higher in WaWa due to this species' apparent preference for the habitat in this reservoir. The longest yellow bullhead collected from East Branch Perkiomen Creek was 295 mm FL. This species was an important pan fish in the East Branch.
2.2.2.3.7.3.7 Redbreast Sunfish Refer to Section 2.2.2.1.7 for information on food habits, parasites and diseases, and human importance for redbreast sunfish (Lepomis auritus). Sunfish larvae were only identified to genus (Lepomis spp.). Spawning of redbreast sunfish, green sunfish, pumpkinseed, and bluegill occurred from June through August in 1973 and 1974. Lepomis spp. larvae comprised only 6%
(0.0128 individuals/m3 ) of East Branch drift in 1973, but increased to 37% (0.14fi9 individuals/mr) in 1974 (Table 2.2-74).
2.2-87
LGS EROL Peak densities occurred in late July in 1973 and mid-June and late July in 1974 (Table 2.2-75).
Redbreast sunfish young ranked ninth in overall abundance in the seine catch (Table 2.2-76). Annual variation in streamwide abundance was moderate, with mean catch-per-unit-effort increasing from 2.0 (<1% of total mean catch) in 1975 to 5.5 (2%)
in 1976. Young were most abundant at E29810 and E32170.
Abundance was lowest near Sellersville (E26630 and E22980), and highest downstream of the treatment plant.
The redbreast sunfish was the fourth most abundant adult fish collected by electrofishing (Table 2.2-80). Streamwide abundance increased from 257 fish/500 m in 1973 to 436 in 1975, probably as a result of populations recovering from severe flooding in June 1972 (Section 2.2.2.3.1). Abundance generally increased in an upstream to downstream direction, except for a depression downstream of Sellersville. Recovery from effects of Sellersville was evident at E12040.
The adult redbreast sunfish was also the fourth most important contributor to streamwide biomass with a mean of 10 kg/500 m (Table 2.2-80). Annual and site trends in biomass were similar to those of estimated abundance.
Redbreast sunfish abundance increased in both Fretz and WaWa from May 1974 to October 1975, probably as a result of a successful spawn in 1974 (Table 2.2-81). The redbreast sunfish was much more numerous in WaWa reservoir than in Fretz.
Growth in length often varied significantly by year-class and location (Table 2.2-86). Growth rates were generally lower at E36020 and increased downstream. Reduced habitat due to intermittent conditions (Section 2.2.2.3.1) and competition may have been responsible for poor growth at E36020. High growth rates downstream were probably due to greater habitat variety and space associated with increasing stream size.
Comparisons of length-weight regressions (Table 2.2-83) between sites indicated that average fish weight was similar at E12040, E30540, and E36020 in both 1973 and 1975. At E36020, fish collected in 1975 were heavier than those captured in 1973.
Stable age structures were observed at E12040 and E36020 in 1973 and E12040 and E1550 in 1975. With minor exceptions, the number of fish in each consecutive age-group decreased (Figures 2.2-19 and 2.2-20). Low abundance of age I fish caused slightly upset age structures at E30540, E22240, and E1550 in 1973 and at E36020, E30540, and E22240 in 1975.
2.2-88
LGS EROL 2.2.2.3.7.3.8 Green Sunfish Refer to the redbreast sunfish (above) for information on spawning periods and larval drift for sunfish in East Branch Perkiomen Creek. Green sunfish (Lepomis cyanellus) young ranked tenth in overall abundance in the seine catch (Table 2.2-76).
The mean catch-per-unit-effort increased from 0.7 (<1% of total) in 1975 to 5.0 (2%) in 1976. The species was somewhat more prevalent in the middle and upstream sections of the creek.
The green sunfish was the second most abundant adult fish collected by electrofishing (Table 2.2-80). Downstream of Sellersville there was an increase in abundance from 1973 to 1975. This was primarily due to increases in the abundance of fish 51 to 90 mm FL, which indicated a good 1974 spawn. Upstream of Sellersville there also was an increase in abundance of this size group, but it was offset by a decline in the number of fish longer than 90 mm FL.
The distribution of adult green sunfish was different from that of redbreast sunfish. Green sunfish reached peak abundance downstream of Sellersville, and gradually decreased in abundance to the confluence. This suggested that green sunfish had a greater tolerance for the degraded water quality downstream of Sellersville (Section 2.2.2.3.1). However, where conditions were suitable for redbreast sunfish, green sunfish may have been at a competitive disadvantage.
The green sunfish was the fifth greatest contributor to streamwide biomass (mean, 7.7 kg/500 m) as shown in Table 2.2-80.
Temporal and spatial variation in biomass was similar to that of abundance. The decline of larger, older fish upstream of Sellersville was also demonstrated by rather large decreases in biomass.
Green sunfish decreased in abundance at both Fretz and WaWa reservoirs from May 1974 to October 1975 (Table 2.2-81). In 1975, spatial differences in abundance and biomass were slight.
Food studies of 14 green sunfish from the Schuylkill River indicated chironomid larvae and pupae, cladocera, cyclopoids, algae, and other plant material were common food items.
Growth in length of green sunfish in 1973 and 1975 consistent among year-classes and sites (Table 2.2-87). Rates of growth in weight were similar between years at E36020, E22240, and E1550 (Table 2.2-83). Average weights of fish upstream of Sellersville were greater than those downstream.
Stable age structures were observed at E36020 and E1550 in 1973 and at all five sites sampled in 1975 (Figures 2.2-21 and 2.2-22). Absence of age I fish caused slightly upset structures at 2.2-89
LGS EROL 1qW E30540, E22240, and E12040 in 1973. Improvement of age structures in 1975 probably reflected recovery from the June 1972 flood (Section 2.2.2.3.1).
2.2.2.3.7.3.9 Pumpkinseed Refer to Section 2.2.2.1.7 for information on food habits, parasites and diseases, and human importance for pumpkinseed (Lepomis gibbosus). Refer to redbreast sunfish (above) for information on spawning periods and larval drift. Pumpkinseed young were low in streamwide abundance and comprised less than 1%
of total mean catch-per-unit-effort (Table 2.2-76). Annual variation in abundance was high, with mean catch-per-unit-effort increasing from 0.4 (<1% of total) in 1975 to 3.0 (1%) in 1976.
Abundance of young was highest in the middle and upstream regions of the creek, and was lowest at E22980 downstream of Sellersville.
The pumpkinseed was the fifth most abundant adult fish collected by electrofishing (Table 2.2-80). Streamwide abundance differed slightly between 1973 and 1975, increasing from .83 to 86 fish/500 m, due primarily to a rise in abundance at E12040 and E1550. This species exhibited a streamwide pattern of abundance
- similar to that of the redfin pickerel. Both species prefer lentic habitat or the quiet water of small streams, which was generally available only in the upstream area of the creek.
Pumpkinseeds ranked ninth in streamwide biomass (mean, 1.4 kg/500 m). Annual and site trends in this parameter were the same as those for abundance (Table 2.2-80).
Pumpkinseeds decreased in abundance in Fretz reservoir but increased in WaWa from May 1974 to October 1975 (Table 2.2-81).
Abundance and biomass were highest in Fretz due to this species' apparent preference for the habitat there.
2.2.2.3.7.2.10 Smallmouth Bass Refer to Section 2.2.2.2.7 for information on growth and human importance for smallmouth bass (Micropterus dolomieui).
Smallmouth bass young were low in streamwide abundance, comprising less than 1% of the total mean seine catch-per-unit-effort (Table 2.2-76). Annual variation in stream abundance was negligible. Young were prevalent only at E1890 and E32170. None were caught immediately downstream of Sellersville (E22980) in 1975 or 1976.
The smallmouth bass was the eighth most abundant adult fish encountered by electrofish/ing (Table 2.2-80). Streamwide abundance increased from 28 to 55 specimens/500 m from 1973 to 2.2-90
LGS EROL 1975, primarily as a result of a twofold increase in number at E1550. Habitat preferred by smallmouth bass was prevalent from Sellersville downstream to the stream mouth. However, this species was abundant only at the extreme downstream reach (E1550). Degraded water quality downstream of Sellersville apparently inhibited smallmouth bass production at E22240 and E12040. The smallmouth bass was the sixth greatest contributor to community biomass (mean, 2.5 kg/500 m). Biomass was also highest at E1550. Although most collected specimens were young, legal-size bass were collected from three of the five sample sites in 1975.
Smallmouth bass comprised only a small portion of the adult fish population in Fretz and WaWa reservoirs (Table 2.2-81).
Estimated abundance decreased slightly in both impoundments from May 1974 to October 1975.
2.2.2.3.7.3.11 Tessellated Darter Refer to Section 2.2.2.1.7 for information on food habits of the tessellated darter (Etheostoma olmstedi). Larvae were collected infrequently in drift; at mean densities of 0.0021 individuals/Mn in 1973 and 0.0001 in 1974, it comprised 1.0 and less than 0.1%
of total drift, respectively (Table 2.2-74). Peak drift occurred in early May 1973 (0.010 individuals/mn) and mid-May 1974 (0.002)
(Table 2.2-75).
The tessellated darter was relatively numerous, comprising 5.8%
of the mean catch-per-unit-effort in East Branch seine collections (Table 2.2-76). Annual variation was high, and mean catch-per-unit-effort increased from 6.0 (2% of total) in 1975 to 30.8 (10%) in 1976. Streamwide variation in abundance was also high, with the species being most prevalent in the upstream reaches of the creek. Abundance was low downstream of Sellersville, an indication of this species' intolerance of poor water quality (Section 2.2.2.3.1).
2.2.2.3.8 Trophic Relationships Refer to Section 2.2.2.1.8.
2.2.3 FARM CROPS, COWS, AND GOATS The 1976 distribution of the principal crop plant communities for the 5 miles surrounding the LGS station are included in sector-by-distance tables of crop production in acres. Tables for wheat, grain corn, corn (silage) and alfalfa, timothy and clover production, and, lastly, a table of total crop production are provided for in Tables 2.2-90 through 92.
2.2-91
LGS EROL The distribution of cows and goats in a 5 mile radius of the station are included in Tables 2.2-93 and 94.
2.2-92
LGS EROL 2.
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LGS EROL 2.2-14 Reisinger, H.J., "Release of Heavy Metals from Contaminated River Sediments," Pennsylvania Academy of Science, 52 (1978) pp 183-185.
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LGS EROL 2.2-26 Flint, O.S., Jr., "Taxonomy and Biology of Nearctic Limnephelid Larvae (Trichoptera); with special reference to species in eastern United States," Entomologica Americana 40.(1960) pp. 1-117.
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LGS EROL 2.2-38 Roback, S.S., "The Immature Tendipedids of the Philadelphia Area (Diptera: Tendipedidae)", Monogram Academy Natural Science Philadelphia No. 9 (1957.) 152 PP.
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2.2-99
LGS EROL TABLE 2.2-1 (Page 1 of 8)
TERRESTRIAL VASCULAR PLANTS POUND ON THE LIMERICK GENERATING STATICR SITE FPCY 1972 TO 1978 Famiv Scientific Namec ) Common Name Equi setaceae Equuseetu arvense Common torsetail Lycopodiaceae LyS~r&it sP Ground pine Opbioqlossa ceae Bctuvbium Mirainianm Rattlesnake fern Polypodiaceae Cncclea nibili Sensitive fern Cbristsias fern Hay-scented fern Aalnu latvneuron Ebony spleenwort TaxuJ baccat a Taxa cea e European yew Pinaceae £.m Pice albies Norway spruce Wbite pine 1.Xeinos Red pine Scotch pine Virginia pine Tkuji occidentalis Northern white cedar Juniverus vrana Red cedar Twipa latifolia Typhaceae Common cattail Alismataceae Saoittari atfl Broad-leaved arrowhead Gramineae Kentucky bluegrass Crchard-qrass LolIu -erene Perennial rye-grass Cigitaria snmninalis Crab grass icbjmocbloa crusgalIl Barnyard grass Setarli esculentus Cyce-rus opp. Foxtai is Cyperaceae Yellow nutgrass Care aiat Awl-fruited sedge Araceas Are=atriobvllu, Jack-in-the-pulpit A. draconti Green dragon Commelin am3uni Skunk cabbage Commelinaceae Asiatic dayf lower Tradescant virainiana Spiderwort Pontederiaceae Beterantbezara nfo Mud-plantain Juncaceae Juncus ef fugus Common rush Liliaceae inealbwx i~~ False bellebore wild garlic Field garlic wild- onion Erlbronium americanz Day-li ly Trout-lily Muscari batriooe Star-of-Bethlehem Grape-hyacinth Polvagcatum biflor True Solomon' s-seal S ilacina racemosae Asparagus False Solomon' s-seal Salicaceae Salix o* ia2 Black willow Biqtooth aspen
LGS EROL TABLE 2.2-1 (Cont' d) (Page 2 of 8)
Fanil Scientific Name(i)
Juqlandaceae Putternut Juaa. cinere Black walnut Litternut hickory Shagbark hickory Mockernut hickory Caryucodioris~ Pignut hickory Sweet pignut hickory Corylaceae American hazelnut Bop-hornbeam Black birch Cormlu amraniflan River birch Gray birch Petuln dentt European black alder Faqaceae Beech Chestnut Chinese chestnut White oak g.qu grlaZ.ndio Chestnut oak Red oak Pin oak
.C. mElzissim Scarlet oak Black oak, Ouru Alba Scrub oak Ulmaceae Slippery elm American elm v2baz1*tinra Backberry Moraceae hnm sanae n Red mulberry Osaqe orange Urtic ace ae Slender nettle
_V. amejjpg Stinging nettle Clearweed False nettle Aristolochiaceae MalrnaY~iLSLDri Wild ginger Polyqonaceae *mooth dock Curled dock Broad dock Pil nzxa1iJ Sheep sorrel Virginia knotweed Pennsylvania .nartie d 1bi1.g.1anadaerian Common umartweed Long-bristled smartveed Lady's thumb Iearthumb Chenopodiaceae Lambs-quarters Amaranthaceae Amaranth pigweed Nyct aqin aceae Four-o' clock Phytolaccaceae Pokeweed Portulacaceae Purelane Spring-beauty
9 EROL TABLE 2. 2-1 (Cont' d) (Page 3 of 8)
Famili Scientific ]Name()
Caryopyllacea* Common chickweed
- s. graminevulaatum Cerastium Lesser stitcbwort Lvcbni. pI* Mouse-ear chickweed Evening lycbnis Bladder campion S. stellat Starry campion Sleepy catcbfly sayonari a offici~.nalig Bouncing bet Diantbus armria Dept ford pink Nymphaeaceas Bullbead-lily Ranunculaceae 4. aerie ]Ridneylea f buttercup Common buttercup R. bulboaui Bulbous buttercup Thlct Hevati olvaamum america Tall meadow rue Blunt-leaved hepatia Anemone 1ii Thimtleweed Aauilecia canadensis Columbine A. XulgaiUi Garden columbine Pefr2bniu aiac1 Garden larkspur CimiciLu racemos Black cohosh Berberidaceae Mayapple BebeAbyunber1ail Japanese barberry Menispermaceae MeniseErum canadens Canada moonseed Maqnoliaceae Tulip-tree Annonaceae Liridenre n tulipif Pawpaw Lauraceae Tlzassia arvese Sassafras Asienatrilob Linder lenzo Common spicebush Papaveraceae eSnuinaria conadnsis Bloodroot CblurdSium f Celand ine Dutchmanf e-breeches Capparidaceae Spider-flower Cruci ferae Tb1smE 121D21 Field pennycress Cow cress Roadside peppergrass M ell& bursa-nastoris Shepherd's purse Calaeam Eda siar sulaaos n osu Black mustard Field mustard verna
- r. Garlic mustard Tumble mustard Dame's rocket Water cress Wintercress Siratis alisi Early winter cress A. XenAi entarioa icoalia Cut-leaved toothwort Spring cress Smooth rock cress Crassulaceae stonecrop Orpine Saxi fraqaceae Early saxifraqe BesaMahli virain ana Foamf lower Hamamelidaceae Wlaamau8 occidentalis Witch-hazel P latanaceae Sycamore
0 LGS EROL TABLE 2.2-1 (Cont'd) (Page 4 of 31 F5rmil~ scientific Namect)
Rosaceae Ninebark Spirea Domestic pear 1). iauiii Domestic apple Sbadbusb Cruaecsmb* im. Hawthorn Common strawberry X. yes woodland strawberry fuSbeenea indLia Indian strawberry EDtentill argenteR Silvery cinquefoil Rough-fruited cinquef oil Pough cinquefoil Dwarf cinquefoil R.DnadeniLs Common cinquefoil white avens Rub~u phoenicol-asi u wine raspberry Red raspberry B.occidentalis Black raspberry
~.alleaheniensis Blackberry AoxAimnJA sp. Agrimony Nultiflora rose Z. carolinl Pasture rose wild plum Peach
- 2. iuJsc.u Sweet cherry Black cherry Chokecherry Lequminosae AliziA iulibrissin Silk-tree Gleditsip tliIaIJ3tbo Honey-locust Partridge-pea
£Czsii canadensis Red-ud wild indigo IzIrioi~u *XZIens Rabbittes-foot clover J. VratZILUA Red clover Alsike clover Smaller hop clover Bzlilotu offiiLnaisz Yellow sweet clover
_".A2.k white sweet clover Birdfoot trefoil Dull-leaf indigobush Black locust C~qmnill1 maria Crown vetch Raked-flowered tick-t cefoil Rfl.J.JgAo Demoiu Panicled tick-trefoil Vicia cracc Cow vetch Oxalidaceae Yellow wood-sorrel D. euroiae Yellow wood-sorrel Geraniaceae Geranni maulati wild geranium Small-flowered cransebill S imarubaceae .9. puskii S Tree of heaven Eupborbi aceae Spurqe
LGS EROL TABLE 2. 2-1 (Contl d) (Paqe 5 of 8)
Scientific Name(&)
Anacardiaceae Smoke-tree Bbn tynbins Staghorn sumac cc.allinr Smooth sumac Dwarf sumac Poison ivy Aquifoliaceae American holly Celastraceae Eittersweet Staphyleacea e aladdernut Aceraceae AM censvivanicum Striped maple
,b. clatanide Norway maple Sugar maple A. nsacbazxii Red maple Silver maple A. neaun Box elder Hippocastan aceae kAzsculu hicrnocastanum Borse chestnut Balsaminaceae Pale Jewelveed 1J.gADesDII Spotted lewelweed Vitaceae jmpelonsi brevivedunculfta Amur ampelopsis Virginia creeper Vitis 1u2lp Frost grape Tiliaceae Basswood Malvaceae Mala neglectI Common mallow M. moschata Musk mallow Velvet-leaf Swamp rose mallow Crimson-eyed rose ma low Flower-of-an-hour Gutt if eras HyIrnicu pgrfoaitu Common St. Johnswort Violaceae Via papiinac Common blue violet
+/-iloba tr Three-lobed violet Cream violet Elaeaqnaceae Russian olive Lythraceae Purple loosestrife Nyssaceae sour gum Onaqraceae Purple-leaved wil low-herb Qenotber &ienniz Common evening primose Biennial gaura Circaea auadrioulcata Enchanter's nightshade Ara liaceae English ivy Umbelliferae Csmobizclayton. Sweet cicely iZ12i axure Golden alexanders Water-hemlock Bcnewort Bnracle maxim Cow parsnip Conus £iZorA Queen Anne's lace Cornaceae Flowering dogwood Red Osier Silky dogwood Red-panicle dogwood Pyrolaceae Spotted wintergreen Mono2oy uniflor Indian pipe
LGSO EROL TABLE 2, 2-1 (Conte d) .(Page 6 of 8)
Scientific Name(i) Common Name Ericaceae Rhododendron uilr Pink azalea Mountain laurel Sixumacia tpacat Black huckleberry Deerberry Early low blueberry Primulaceae _V.vailhEl1an1 Whorled loosestri fe Moneywort A.mciliat Aaal arvensis Fringed loosestri fe Scarlet pimpernel 01eaceae Frxn americana SyrinIa vlaaris Wbite ash Common lilac Apocynaceae VInoa min ne Myrtle
-~cyu cannainno Indian hemp Asclepiadaceae Butterfly weed A.incarniat Swamp milkweed white milkweed Common milkweed Convolvulaceae Ikmoa coccinn Small red morninq-qjbry I. bederacea Ivy-leaved morning-glory I. npureau Common morning-glory Convolvulus semni Hedge bindweed
.C.arvensi. Field bindweed Polemoniaceae PblOx ,ubu lata mNes phlox Boraqinaceae Libsemmarvense Corn grouwell True forget-me-not Virginia cowslip Vertenaceae White vervain Blue vervain Latliatae Tricboste ico-am Bluecurls Teucrju canadens* Germander Mad-dog skullcap Neyeta cataria Catnip Prunella IY~h fistulasvuar Beal-all Glechoma hederacea Gill-over-the-ground Leonurus cardiaca Motherwort Lmuamplexicaule Dentit L. DUDDure Stacby i Purple dead nettle Pough hedge-nettle Monarda ddy Bee-balm liah3zpb 1hrsuta Wild bergamot L4.~ sazninii Hairy wood-mint Pvcnantbemum vi i um American pennyroyal Lvcom u iniM u Virginia mt. -mint Mentba spicat Buqleweed Spearmint Solan dulcana Peppermint Solanaceae European bittersweet Common nightshade Horse nettle R. beteroybMZ l Smooth ground cherry atura ezamoni Clammy ground cherry Jimeonweed
LO ,_ROL TABLE 2.2-1 (Cont'd) (Page 7 of 8)
Zamily Scientific Name(') Cmon Name Ye rbascui thacus Common mullein Scrophulariaccae Motb mullein
_V. blattaria Fenilwortb iw LinariA vulgaia Butter-and-eggs Figwort rjibjlg alahra Turtlebead Peotemo2 digiais*i Foxglove beardtonque Hairy beardtonque Princess-tree Mimlu~JI ringens Square-stemmed monkey-flower Veg ic oficnali Common speedwell Slender speedwell Ivy-leaved speedwe 11 Biqnoniaceae Cata bs~mI.21J.J j Trumpet Creeper Catalpa Ecfau zvirinia Peechdrops Orobanchacea e One- flowered cancerro ot Cro~banche iniflor~ lopseed Phrymaceae Broad-leaved plantain Plantaqinaceae Narrow-leaved plantain Rubiaceae Cleavers
- 2. .ancflat~ Fragrant bedstraw t.
mfloru Wild madder Rough bedstraw Eluets Capri foliaceae European honeysuckle Bos onciacagrucs.r.ISI1e Fly-honeysuckle Japaneee honeysuckle Coralberry
- y. adentatu Hobblebush wild raisin Smooth blackhaw Arrow wood Zsymccr.ayc lorbatat Maple-leaved viburnum Common elder Vi-u ainifol Teasel Dips acaceae Bur-cucumber Cucurbitaceae cassistulosui wild cucumber pruaerfoliaum Venus' s looking-glass Campanulaceae Great lobelia a eriotinum E.g cue anaens Indian tobacco new York ironweed Compositae Spotted Joe-pye weed Hollow joe-pye weed Boneset S&.inla Late-flowering thorouqhwort Ve. lncea oeoans White snakeroot Buy orEiummault Blue-stemmed goldenr d Large-leaved qolden rod Silver rod Early qoldenrod Gray goldenrod
LGS EIRCL TABLE 2.2-1 4Conted) (Page 8 of 9)
Scientific INamef 1) Common Name Compositae (cont'd) Pough-stemmed goldenrod S. .ruclosm Canadian goldenrod Lance-leaved goldenrod S. +/-.D3JitUli Grass-leaved goldenrod Aster sobreberi Schreberes aster A. crifg.1ius Heart-leaved aster A.novae-analiae Few England aster A- renanthoides Crooked-stemmed aster Smooth aster Beath aster Lowriegs aster Caisy fleabane
.Z. Dlbiladelohicus Ccmmon fleabane Antennaria sp. Pussytoes znaybaliJ maraaritaceae Pearly everlasting Great ragweed
- h. artemisiifolia Common ragweed Xan+/-.bium chinens. Cocklebur Green-headed cone flower Tbin-leaved coneflo~eer Black-eyed Susan Helianthus aDDn13 Common sunflower Noodland sunflower j.decaoetalus Thin-leaved sun flower Jerusalem artichoke Beqgar-ticks Tickseed-sun flower Gal insoga Aghilla millefoli ur Yarrow Nayweed Chrysanthemum leucntbeum Cxeye daisy Nugwort Great burdock Airaa vyaa Bull thistle Canada thistle Cgturme nigra Black knapweed American knapweed Chicory Yellow goat' s-beard Common dandelion Spiny-leaved sow thistle B. ncusnuiie Field sow thistle Lactuc sarioAl* Prickly lettuce wild lettuce B. floiunum Mouse-ear hawkweed Smoothish hawkweed pratens~UI~3 Ring devil vensu Rattlesnake weed (1) Peference 2.2-2
LGS ERCL 1APIE 2.2-2 AMPHIBIANS AND REPTILES POUND ON THE LIMERICK GENERATING STATION SITE FROM 1972 TO 1978 Scientific Name(') Como 1amc 1 Amphibians salamandridae Notocbtbilmus vixjdscl Red-spotted newt P lethodontidae Dusky salamander P1letbodn cAinere Re6-backed salamander Pseudotiton xnuse Red salamander Sumac lnacauda Long-tailed salamander Two-lined salamander Bufonidae &&J2 americamE American toad
]Ufr2 wcoose fowleri Fomleres toad Hylidae Spring peeper Ranidae IMciciens leopard frog Pickerel frog AM £Dl1E+/-ita Bullfrog Green frog Reptiles Chelydridae Cbelgdr servnti Snappinq turtle Stinkpot Testudinidae Spotted turtle Tgrravn nkrcint wood turtle Chsmys ciun1 Box turtle Painted turtle Colubridae Water snake Thamnonh+/-E £1i+/-A11 Garter snake DPadobia pngaus Ringneck snake ColukIX £2DU1Z1ik2 Black racer
(')Reference 2.2-4
LGS EFOL, TABIE 2.2-3 SAMPLING HISTOFY FOP ECOLOGICAL STUDIES OF BIRDS ON THE LIMERICK GENEPATING S¶ATICN SITE Sep 1972- Apr 1973- Apr 1974- Apr 1975-Program/Sites Mar 1973 Mar 1974 Mar 1975 Mar 1976 Waterfowl Schuylkill River S85000-S72000 X X X Breedinq Birds
]B 1 x X X BB2 X X X Winter Birds WB1 X P2 I BB1 X X EE2 X X Miqratinq Birds Chester County Route I X X X Montqomerv County Route X X X X Bird Mortality at Meteoroloqical Towers Tower 1 X X Tower 2 x X
LGS EROI TABLE 2.2-4 (Paqe I of 4)
BIRDS FOUND WITHIN AN 8-KM RADIUS OF LIMERICK GENERATING STATICO FROM 1972 to 1978 Occurrence in the Scientific Name(I Common Name (1) Delaware Valley Region (2) win Spr Sum Fall Gaviidae Gazia Jiusz Common loon PC C VC C Podicivedid ae Horned qrebe C tpC Uc PC Pied-billed grebe PC FC FC PC C Pod ilvmbus pd2iLS3 Phalacrocoracidae Phlarocorax aurituS Double-crested cormorant UC PC UC PC Ardeidae Ardea, beo Great blue heron UC C C C Buto rides viesen~ Green heron C C VC Great egret .PC FC PC DC Snowy egret Tic PC DC PC PC Louisiana heron PC DC Black-crowned night heron FC C Nyficr- nvcicraz Yellow-crowned night heron DC DC C Nyctanassa- vigoss. FC UC UC Least bittern FC PC American bittern VC FC PC PC FC PC Anatidae Mute swan DC PC DC p_12X iaplmbanu Whistlinq swan PC PC C Brnn. canadensis Canada qoose UC TC UC
,ghe caerulescens Snow goose C UC C C Aft" platv~bxncbo Mallard VC PCC C C A.zykzi~ Black duck DC PC DC FC Pintail UC Green-winqed teal UC VC PC UC VC DC Blue-winqed teal Tc FC American wigeon FC PC PC UC C A.clvoeata Northern shoveler PC PC Wood duck VC PC UC UC A. mzmw~ Canvasback PC PC DC Greater scaup PC PC DC Lesser scauF PC PC PC Bucepbala clanmaul Common goldeneye PC UC VC D. albepla Buff lehead C FC PC Oldsquaw C C PC Ruddy duck C PC PC Loyhodytes cucullatus Hooded merganser UC PC UC UC Common merqanser C UC DC Turkey vulture C PC C Cathartidae Catbartes ~aura PC UC PC Accipitridae Sharp-shinned hawk UC Cooper's hawk DC DC A. coovrRA Fed-tailed hawk PC TC VC PC UC PC UC A. l~ineflii Ped-shouldered hawk UC PC Broad-winged hawk UC FC Dc FC PC
,a.plnatyRp!xus Marsh hawk Uc PC UC PC FC Pandionidae Osprey UC DC Falco perarinu Pereqrine falcon PC PC UC Falconidae FC C E. SMXIIZJJL American kestrel FC FC FC Buffed grouse PC Tetraonidae Bonam umbellu FC PC PC Phasianidae colinus virginianyw Bobwhite C PC PC PC Ph~asianus colbicu. Pinq-necked pheasant UC DC UC Rallidae Porzan arolmiM So ra
IGS EPot TABLE 2.2-4 (Cont'd) (Paqe 2 of 4)
Cccurrence in the Famili Scientific pftmge (,) Common Name (1) Delawarg Valley Reolcn (2)
Win Spr Sum Fall Ful americ~a American coot C C DC UC C Charadriidae Filldeer UC PC VC Scolopacida e Philohela minz American woodcock UC Pc UC PC caell allna Common snipe uC PC PC Acti~j *_macula Spotted sandpiper DC Tic PC VC Tringa solitari Solitary sandpiper DC UC VC
- 1. f sjay Lesser yellowleqs UC UC DC PC alwdri m l Pectoral sandpiper PC UC VC least sandpiper Uc PC FC 0C Phalaropodidae Semipalmated sandpiper uc VC FC PC Lghiml lobatus Northern phalarope DC UC VC Laridae Laru arcentat Herring qull C PC C C L. deslay~ren.1 Rinq-tilled qull PC PC PC PC Columbidae 1-umbU lr viacroura Rock dove C C C C Zead Mourninq dove C C C C Cuculidae Coou rricanus Yellow-billed cuckoo PC VIC C. ervthropthalmus Black-tilled cuckoo PC tc Tytonidae
- vto Alba Barn owl FC PC PC C C FC Str iqida e Screech owl PC C D~b virainiang Great borned owl PC PC PC Cap rimul qidae Common niqhthawk PC PC Chael&= velagica FC C UC Avodidae Chimney swift C Trochilidae A lobscolubris Ruby-tbroated hummingbird PC PC UC PC PC Alcedinidae megagrlek Al* n Belted kingfisher PC UC C PC C Picidae *SD+/-DeN AJJZatul
_%I&"~ £~u Common flicker PC Red-bellied woodpecker PC PC PC M
Ce~ntaMcoflihng melaerpes bi~
erytrzr oebalus DC UC Ft Dc Red-beaded woodpecker Yellow-bellied sapsucker UC PC pendroicus villosus PC PC DC PC Hairy woodpecker
- p. .pubescen Downy woodpecker C C C cc Tyrannidae TyrajM tyrannus Eastern kingbird PC C PC mv hgb rinitus PC PC PC UC Great crested flycatcher Eastern phoebe UC PC PC VC mvi.n minimu+/- tC DC PC UC least flycatch~er Contopas yieSM Eastern wood pewee FC PC PC PC FC PC Alaudidae Dorned lark Hirundinidae ig onebicolor Tree swallow UC PC DC Bank swallow PC PC c PC EC DC Stlioreyrficcilig Rough-winqed swallow C Hi _*n r~stica Barn swallow UC PC PC DC Proane sg.!2 Purple martin PC PC PC Cya nocitta g is a Blue jay PC C C PCC Corvidae Cory* bracbvrbvncbcs Common crow C C PC
_q.ossifraggs Fish crow FC FC PC PC PCC Paridae Pars atricavillus Black-capped chickadee C PC PC Carolina chickadee C C C C FC Sacaxolnensis Tufted titmouse UC PC White-breasted nuthatch FC PC Sittidae PC PC
- g. canadensi* Red-breasted nutcbatch
IGS EROI TABLE 2.2-4 (Cont' d) (Paqe 3 of 4) occurrence in tbe scientific NaMe( 1) Common Paie (I) Delawaxe Valley Regton (2)
Win Spr Sum Fall Certhiidae Certhi~ frz liaris Brown creeper FC PC C PC Troqlodvtidae House wren - FC C PC Winter wren UC VC - Dc Tbyrotboru I4doiicianus Carolina wren PC FC PC FC Mimidae Mockingbird C C C C Gray catbird - PC C FC Brown thrasher - UC FC DC Turdidae American robin - C C C Trdu~sb~ mi-araonl Wood thrush - PC C PC Bermit thrush cC PC UC TC Byoih msei Swainson's thrush - FC VC FC Gray-cbeeked thrush - UC UC VC Catargauta Veery - PC UC PC Sylviida e Blue-gray gnatcatcher - PC PU VC Golden-crowned kinglet uC PC UC C Ruty-crowned kinglet cC 0C - PC Motacillidae water pipit UC OC - DC Bombycillidae Cedar waxwinq uC UC UC 0C Sturnidae R. ckialendul Starling C C C C Vireonidae White-eyed vireo - PC PC PC Yellow-throated vireo - 9C DC UC Solitary vireo - tC UC DC Red-eyed vireo - VC VC 0C Parulidae .Y. f la.W Black-and-vl~ite warbler - PC PC PC Golden-winged warbler - VC VC -
Blue-winged warbler - VC PC UC Tennessee warbler - UC DC DC Nashville warbler - UC UC 0C Northern parula - VC UC VC
_V. FLgin - VC PC DC Yellow warbler
- 2. .l amerigg Cape May warbler UC VC UC DC Black-throated blue warbler - UC VC VC D. tiri~ Yellow-rumped warbler cC PC - EC ca.ruensv'lvni Black-throated green warbler - PC DC PC Blackburnian warbler - UC VC VC
- 2. coroat. - DC DC PC LP. vLDJW Cbestnut-sided warbler Blackpoll warbler - PC VC (C R. ijn.Lc UC PC FC FC Pine warbler Prairie warbler - PC C PC Palm warbler VC PC - FC D. ioilnglJ i- - PC C PC
~s~thriatrca Cvenbird louisiana waterthrusb - UC PC DC Kentucky warbler - VC FC VC Rilmar Connecticut warbler - UC - .C aiuPrnaurcailus Common yellowtbroat VC PC C FC Yellow-breasted chat tc UC PC DC Canada warbler - UC FC EC American redstart - PC VC PC
.GS EROL TABLE 2.2-4 (Cont'd) (Paqe 4 of 4)
Cccurrence in the laaily Scientific Nae (1) Common~ Name (1) Delauare Valley R-gjn (I)
Win Epr Sum Fall Ploceidae House sparrow C C C C Icteridae Sturnellmaygna, Eastern meadowlark PC C C C Aie lais phgeiceu Red-winged blackbird C C C C Orchard oriole 3C UC UC S albula Northern oriole FC C
,VA~gM caroli nus Rusty blackbird UC UC C OuiLsIcal guiscula Common qrackle C C C PC I1Q19thus! A&S Brawn-headed cowbird PC PC PC PC Thraupidae giranq~ olivacep Scarlet tanaqer PC PC C Frinqill ida e CarSinalis cardinalis Cardinal C C C PC Pheucticus ludovicianus Rose-breasted qrosbeak PC PC Passerina cyanca indigo buntinq UC C UC Hesperichona veseriz+/-j Evening grosbeak PC PC PC PC Purple finch PC PC VC PC House finch C FC UC VC Acantbi~ flammea Common redpoll DC UC PC Soinus vi Pine siskin UC UC 'C American qoldfinch C C C DC Loxij leucop-tera White-winqed crossbill DC UC PC PipjJ& erythrophtbaluusg Ru fous-sided towhee UC FC C AmModramus gjavannruni Grasshopper sparrow UC UC Cc Dark-eyed junco C PC DC PC Spilell~ arborca Tree sparrow C PC PC Chippinq sparrow PC C PC cc Field sparrow PC FC White-crowned sparrow C UC cc
.zongtrig~bia. leucchxxM CC white-throated sparrow DC C cc Passerella iliaca Fox sparrow DC UC tcPC UC CC Lincoln s sparrow CC B.jU7a Upcolnii Swamp sparrow FC PC PC geoJaian C C C Sonq sparrow C Winter December, January, February Sprinq March, April, May Summer June, July, Auqust Fall = September, October, November Cu Common PC Fairly common
-C = Uncommon DC=
Not present
( ) Reference 2.2-7 C*) Based upon Brady et al. (Ref 2.2-8) who defined Delaware Valley Reqion as the area bound by the Pocono Mountains of Pennsylvania in the north and by Cape Henlopen, Delaware to the south east by the New Jersey coast between the Shark River and Cape May; and to the west bv the limits of the Delaware drainaqe.
0 0 LGS EROL TABLE 2.2-5 IMPORTANT BIRD SPECIES SELECTED FCR 7EE LIMERICK GENERATING STATION SITE AND CRITERIA POP SELECTICV INPCP7AT CRITERIA to Plant Ccoling Cooling special Commercial or Ecological lower Tower Blowdown Species Interest Recreational Value Importance Collision Drift Discbarqe Canada qoose x x x x x Mallard x x x x Black duck x x x x x Great blue heron x x x x Common merqanser x x x x x Osprey X(1) x x x Rinq-necked pheasant x x x American kestrel x x Common crow x x x Common' yellowtbroat x x x Sonq sparrow x x x
(&)Listed as "status undetermined" Office of Endanqered Species and International Activities, Ref. 2.2-5.
LGS ECTCL TAEIE 2.2-6 MAMMALS FOUND CN THE LIMERICK GENERATING STLItION SITE FROM 1972 TO 1978 Scientific Name (1) Comorn Name (1)
Didelphi ida e Didelphis marsupialis Cpossum Tal pidae Scalovus aguaticus Eastern mole Soricidae Plarina brevicauda Shcrt-tailed shrew Ve spertilionidae Pipistrellus subflavus Eastern pipistrel Lasiurus borealis Red tat Pro cyon idae Procyon Iotor Raccoon Mustelidae Mustela frevata Lonq-tailed weasel Mephitis mephitis Striped skunk Canidae Vulpes fulva Red fox Urocyon cinereo arcrenteus Gray fox Sciuridae Marmota monax Woodcthuck Tamias striatus Eastern chipmunk Tamiasciurus budscnicus Red squirrel Sciurus carolinensis Gray squirrel Cricetidae Peromvscus l5ucopu White-footed mouse Mi crotus pennsvlvanicus Meadow vole Ondatra zibethicus Muskrat Muridae Mus musculus House mouse Rattus jreicus Ncrway rat Zapodidae zapu hudsonicus Meadow jumpinq mouse Leporidae Svlvilag* floridanus Eastern cottontail Cervidae Odocoi leus virainianus White-tailed deer (C) Reference 2.2-10
TABLE 2.2- 7 (Page I of 3)
SUMMARY
OF COLLECTIONS MADE FROM THE SCHUYLKILL RIVER, PERKIOMEN CREEK, AND EAST BRANCH PERKIOMEN CREEK BY PROGRAM AND YEAR, 1971-1978 Schuylkill River Program 1971 1972 1973 1974 1975 1976 1977 1978 Water Quality - - - 42 86 144 168 Phytoplankton - - 29 43 -
Periphyton1 - - 49 36 -
Macrophytes2 3 Benthic Macroinvertebrates3 - 26 36 34 22 35 Macroinvertebrate Drift' - 264 132 114 72 Larval Fish Drifts - - - 218 504 880 Larval Fish Trap6 .... 82 Larval Fish Push Net7 104 Seine@ ... . 132 132 Small Fish Population Estimates' - - 30 12 21 11 Large Fish Population Estimatesi 0 - - 37 17 14 23 Large Fish Catch per Unit Efforts' 30 55 44 Vincent-Trap Net"z 3
154 116 120 122 70 130 Age and Growth' Redfin pickerel White sucker - - 303 68 Brown bullhead - - 241 132 Redbreast sunfish - - 51414 88 Green sunfish Pumpkinseed - - 337 66 Smallmouth bass
Table 2.2-7 (Cont'd) (Page 2 of 3) fl W% nfl - qfl,' 4fl 4fl~ 4-6 4fl*~ 4fl10
&MM&M JZ.Lfi Jala JZIM Zia j ZiR 4 flI~
JZIA jzIO Water Cuality - - 14 24 24 Phytoplankton - - 11 Periphyton - 14 - - -
Macrophytes Benthic Macroinvertebrates 22 24 i8 - 22 Nacroinvertebrate Drift 12 84 72 -
Larval Fish Drift - 479 514 504 696 Larval Fish Trap - - - 84 240 Larval Fish Push Net Seine - - - 64 65 Small Fish Population Estimates - - - 12 12 Larqe Fish Population Estimates - - 9 2 15 Large Fish Catch per Unit Effort Vincent Trap Net Aqe and Growth Redfin pickerel White sucker .... ¶164 Brown bullhead Redbreast sunfish - 231 - - 249 Green sunfish - 103 - - -
Pumpkinseed Smallmouth bass - 82 - - -
Table 2.2-7 (Cont'd) (Page 3 of 3)
.S.u..kill River Program 1972 1973 1974t 1975~ 1976 1977L1978 Water Cuality - - 70 120 120 120 Phytoplankton Periphyton - 28 81 -
Macrophytes Benthic Macroinvertebrates 66 72 54 - 611 Macroinvertebrate Drift - 84 69 -
Larval Fish Drift - 136 56 -
Larval Fish Trap Larval Fish Push Net Seine - - - 87 80 Small Fish Population Estimates Larqe Fish Population Estimates o 10 4 14 Larqe Fish Catch per Unit Effort Vincent Trap Net Aqe and Growth Redfin pickerel - 37 214 White sucker - 172 Brown bullhead Redbreast sunfish - 1119 210 Green sunfish - 558 204 Pumpkinseed Smallmouth bass t One sample consisted of four sample units.
8 One sample consisted of oae aerial survey.
3 One sample consisted of four sample units for the Schuylkill River (1972-1976) and for Perkiomen Creek and East Pranch Perkiomen Creek (July 1973-1976). Five sample units comprised one sample for Perkiomen Creek and East Branch Perkiomen Creek (Jan 1972-June 1973).
4 One sample consisted of two sample units.
5 One sample consisted of one net contents per unit time per site per date (time unit is usually I hour on the Schuylkill River and Perkiomen Creek and 4 hours4.62963e-5 days <br />0.00111 hours <br />6.613757e-6 weeks <br />1.522e-6 months <br /> on the East Branch Perkicmen Creek).
6 One sample consisted of one net contents per unit time per- site per date.
(time unit is usually 4 hours4.62963e-5 days <br />0.00111 hours <br />6.613757e-6 weeks <br />1.522e-6 months <br />).
7 One sample consisted of one site per date.
- One sample consisted of one date per site.
9 One sample consisted of one electrofisbing pass per site date (one population estimate is determined from 3 passes at a site per date).
10 One sample consisted of one date per site (dependinq on type of estimate, 2-8 dates per site per year constitutes one population estimate).
It One sample consisted of one date per site.
Is One sample consisted of one net day per site.
Is One sample consisted of the number of specimens per species.
14 These fish were collected from Culvert Creek, a tributary of the East Branch Perkiomen Creek, approximately 235 m from the East Branch confluence.
LGS EROL TABLE 2.2-8 (Page I of 3)
NUMBER OF SAMPLES BY YEAR, PROGRAM, AND SITE COLLECTED FROM THE SCHUYLKILL RIVER, 1971-1978 (1)
Program/Sites 1971 1972 1973 1274 1975 1976 1977 1978 Water Quality S77440 14 24 S77660(2)
Sublocat ion 1 24 24 Sub location 2 24 24 Sublocation 3 24 24 S77140 14 24 24 24 S77040 14 24 24 24 S73880 14 24 24
.w S72500 24 Phytoplankton S77720 29 43 Periphyton S77580 - - 25 9 - - -
S77260 - - 24 27 - - -
Macrophytes - - 1 3 Benthic Macroinvertebrates S78620 8 12 12 12 s76760 11 12 10 12 S75770 7 12 12 11 Macroinvertebrate Drift s77560 - 132 132 144 72 - - -
S75770 - 132 - - 11 Larval Fish Drift S77560 - 218 504 880 Larval Fish Trap S77560 -- - - 82---
Larval Fish Push Net S78973 S78432 -- - -- -- - 8 S77970 -- -- - -- - 8 S77550 -- --
Q
-8 8
S77485 - - - -8 S77320 -- - -- -- - 8
- - - -8 S77230 S77161 -- -- - -- - --- -8 8 S76970 S76840
0 IGS EROL TABLE 2.2-8 (Cont'd) (Paqe 2 of 3)
Program/Sites 1971 1972 1973 197_4 1975 1976 1977 1978 Larval Fish Push Net S76794 - - - - - 8 - -
S76632 - - 8 - -
S75781 - - - 8 - -
Seine S817 50 - - - - 12 12 - -
S78900 - - - - 12 12 - -
S78460 - - - - 12 12 - -
S77960 - - - - 12 12 - -
S77240 - - - - 12 12 - -
S77220 - - - - 12 12 - -
S77010 - - - - 12 12 - -
S76840 - - - - 12 12 - -
S76820 - - - - 12 12 - -
S76310 - - - - 12 12 - -
S75730 - - - - 12 12 - -
Small Fish Population Estimates S78140 - - 3 - - - -
S780140 - - - - 3 - - -
S77940 - - 3 - -..
S77740 - - - -.
Sublocation 1 - - 3 - - -
Sublocation 5 - - 3 3 3 3 - -
877640 - - - 3 3 3 - -
S77440 - - 3 - 3 - - -
S77140 - - 3 3 3 - - -
S77040 - - 3 3 3 3 - -
S76940 - - 3 - - -
S76640 - - 3 - 3 2 - -
S76540 - - 3 - - -
Large Fish Population Estimates S79400 - - - 5 - - 5 -
878040 - - 8 - -
S77240 - - 9 3 7 - 6 -
876440 - - 10 3 7 - 6 -
S760140 - - 10 - - -
S74365 - - - 6 - - 6 -
Larqe Fish Catch-per-Unit-Effort S79310 - - - - - 6 10 8 S77640 - - - - 6 9 9 S76940 - - - - 9 9 S76440 - - - 6 10 9 S74365 - - - 6 9 9 872885 - - - 6 8 -
0 IGS EROL SABLE 2.2-8 (Cont'd) (Paqe 3 of 3)
Proar am/Siteg 1971 1972 1271 1974 1975 1976 1977 1978 Vincent Trap net S73810 32 23 24 25 l4 26 S 3800 32 23 24 25 141 26 S72960 32 241 24 25 111 26 S72950 30 22 24 24 141 26 S72120 28 24 34 23 14 26 Aqe and Growth S79310 White sucker Brown bullhead - 33 - 111
-Redbreast sunfish Pumpkinseed - 117 -
S77240 White sucker - 127 -
Brown bullhead - 111 -
44 Redbreast sunfish - 265 - 43 Pumpkinseed - 62 - 23 S76440 White sucker - 176 -
Brown bullhead - 66 - 24 33 Redbreast sunfish - 279 - 115 Pumpkinseed - 228 - 113 S72885 White sucker Brown bullhead - 31 - 37 Redbreast sunfish Pumpkins eed
(')see footnotes in Table 2.2-7 for definition of what constitutes one sample.
(C)See Subsection 6.1.1.1.1 for a description of these sublocations.
LGS EROL TABLE 2.2-9 (Page 1 of 2)
NUMBER OF SAMPLES BY MONTH, PROGRAM, AND YEAR COLLECTED FROM THE SCHUYLKILL RIVER NEAR LIMERICK GENERATING STATION, 1971-1978 (1) grogram, Year Jan Feb Mar Apr ay Jun Jul Aug *p Oct Nov Dec Water Quality 1974 6 6 6 6 6 6 6 1975 6 6 6 6 6 8 8 8 8 8 8 8 1976 12 12 12 12 12 12 12 12 12 12 12 12 1977 14 14 14 14 14 14 14 14 14 14 14 14 Phytoplankton 1973 .. ... 4 5 4 4 5 4 3 1974 4 4 4 4 5 1 2 4 4 4 4 3 Periphyton 1973 - - - 4 8 8 8 5 10 2 4 1974 1 2 3 1 4 1 2 6 6 7 3 Macrophytes 1974 1977 Benthic Macroinvertebrates 1972 2 2 1 3 3 2 2 3 3 2 3 1973 3 3 3 3 3 3 3 3 3 3 3 3 1974 3 3 3 3 3 3 3 3 3 2 3 2 1975 2 2 2 2 2 2 2 2 2 2 2 1976 2 3 3 3 3 3 3 3 3 3 3 3 Macroinvertebrate Drift 1972 12 12 12 12 12 12 12 12 12 12 12 1973 12 12 12 12 12 12 12 12 12 12 12 1974 12 12 12 12 12 12 12 12 12 12 12 12 1975 12 12 12 12 12 12 Larval Fish Drift 1974 40 '48 40 32 34 24 1975 72 144 72 144 72 1976 180 308 200 192 -
Larval Fish Trap 1975 12 24 12 24 10 Larval Fish Push Net 1976 .. .. . 26 39 39
0 EGS EFOL IABLE 2. 2-9 (Contvd) (Page 2 of 2)
Proaram/Year Jan 1iA inA Jun "Ia Aml ~ Oct Nov Dec Seine 1975 11 11 11 1976 11 11 11 Small Fish Population Estimates(&) -
Larqe Fist Population Estimates(R) -
Larqe Fish Catch per Unit Effort 1976 5 5 5 5 5 5 1977 - 6 6 6 6 6 6 6 6 1 4. 2 1978 - 5 5 5 5 5 5 5 4 5 Vincent Trap Net 1971 - - 10 28 40 26 20 20 10 1972 - - 19 10 20 20 20 19 8 1973 - - 10 20 20 20 20 20 10 1974 - - 20 20 20 20 14 20 8 1975 - - 10 10 10 10 10 10 10 1976 - - 20 20 20 20 20 10 20 Aqe and Growtb(c)
(')See footnotes in Table 2.2-7 for definition of what constitutes one sample.
(2)Samples for these proqrams were not included because only annual data-was utilized.
LGS EROL TABLE 2.2-10 (Page 1 of 4)
LISTING OF PHYTOPLANK¶ON TAXA WITH QUARTERLY (SEASONAL) DENSITIESCI) PER TAXA COLLECTED FROM STATION S77720, SCHUYLKILL RIVER, LIMERICK GENERATING STATION, 1974
%inter Sprinq Taxa Pin Max Mean Mi Max Mea, Cloropbvta Eudorina - 500 45 - 2.000 182 lleodori a ...
uglygA-Cblorcocum ... 4,000 3614 Anki1trodesmus 11000 5,000 1,612 2,000 93.000 26,727 lircbneriella - - - - 2,000 272
- - - 32,000 3,455 Errerel1a .- - 2,000 182 icractinium -.. - 3.000' 636 Dictyosybaerium - - -
Coel~asrum- - - -
Scenedesmus - 1,000 227 4,000 34.000 8.910
- 1.000 90 - 3,000 545 stim -.... - - 1.000 91
....- 1,000 5145 i- 1u33, 121 - - -
.l..i 21000 2,273
.os*loipom-6 - - 4.000 909
....- - 2.000 1455 Euq lenophyt a Eualena - - - -2,000 1451 Pyrrhopbyta Bacil1lariophyt a
.riunob yo - 2,500 1,197 - 10,000 14.000 Callosonas - 2,000 182 - 2,000 3624 i- 500 15 - - -
sidu- .... 2.000 182 e2,000
- 2.668 4014,000 16,008 105.561 6,137 63.000 2,000 518.000 53,000 218.636 15,545
. -.... 1,000 273 Sinodiss- 1,000 91 - - -
LGS EROL TABLE 2.2-10 (Cont'd) (Page 2 of 4)
Winter Spring 212M Min Max Mean Min .gax_ ean Bacillariophyta (cont.)
Alterionella 3,500 22,000 11,743 6.000 32,000 15,455 Diatom 1,500 17 000 5,910 2,000 96,000 24,455
- 2,000 712 - 14,000 4,364 51000 43,000 16,092 23,000 240,000 70,090
- 11,000 3,500 - 7,000 2,091
- - -. 9,000 2,636
' *.l1.Ii - 500 45 - - -
Achnanthes - 4,669 1,364 - 2,000 4,727
- 5,000 1,409 - 16,000 7,636 G.rosia - 1,000 152 - 3,000 818
.Eavicula 24,500 199,000 83,035 205,000 1,162,000 492,545 P1jnularia - 1,334 485 - 5,000 818 Gomphonema - 11,000 2,773 - 10,000 4,545 C bella 1,334 10,000 3,940 3,000 61,000 18,545 pitzecbia 8,500 69,000 24,153 18,000 170,000 52,091 Cvmatopleura - 1,000 91 - - -
" i - 500 91 - 3,000 818 unotia - 2,000 182 - 4,000 455 Staurnxni~ - -- - - -
Fboicoaxphenia - - - - --
Cyanophyta coeloohaerisa - - - - -.
hococs- - - - -
Mcoyts- - - - --
Gooas- - - - --
stic~hospo - - - - --
nbfa - - -......
- 1,000 273 - 1,000 364 Anabaena - 1,000 242 - 10,000 2,091 Ahanizomeno - - - - -
Cylindrosperutum ------
Total 50,002 837,512 271,559 328,000 2,661,000 989,544
LGS EROL TABLE 2.2-10 (Cont'd) (Page 3 of 4)
Summer Fall IMx Min MAX Mean Min Max Mean Cblo rophyta Rudorina...
Gotm- 1,000 222 - - -
Fandorina .....
VolvoiA - ---
Clorococcum - 46,000 23,555 - 69,000 9,500 Ankistrodeamug 3,000 102,000 59,444 14,000 242,000 62,583 Kirchneriellp - 17,000 5,111 - 27,000 4,083 1,000 134,000 44,000 - 27,000 7,167 Errerella .....
Mr - 2,000 555 - - -
Dictvosvbaerium - 28,000 333 - 50.000 9,833 Astinastrum 1,000 87,000 28,222 - 8,000 1,500 QfelatX1m - 82,000 28,889 - 51,000 9,583 cehnedesmi3s 6,000 668,000 235,444 2,000 548,000 114,917 S rod ict yon ......-
6,000 280,000 86,778 - 156,000 24,000 Otis - 12,000 2,667 - 6,000 500 1othri - 14,000 556 - - -
-- - - 8,000 1,750
- - - - 2,000 250
.Mou- '4,000 778 - 6,000 1,167 beti2m - - --
--zotxi 26,000 7,222 - 18,000 6,167 Cosmi - 2854,000 48,333 - 9,000 3,250 Zaynnema - 8,000 1,111 - - -
1,000 '42,000 10,444 - 22,000 4,000 Euqlenophyta Euoe- 54,000 444 - 40,000 3,5417 1bhacu - ---
Pyrrhophyta Cerat - 7,000 1,000 - -
Bacillariophyta
- 1,000 111 - 33,000 6,583 Mafll32mE - - - --
8ynur - 1,000 111 - - -
Coscinodiscus - 12,000 2,333 - 3,000 500 16,000 306.000 161,000 16,000 140,000 62,583 Melosi - 254,000 87,667 1,000 96,000 34,333
- 1,000 444 - - -
Ste-hanodiscu 17,000 3,222 6,000 194,000 40,000
0 LGS EROL TABLE 2.2-10 (Cont'd) (Page 4 of 41 Summer Fall MLin... M.axL.. mean bin Ma Mean Bacillariophyta (cont.)
- 3,000 556 - 318,000 60,333 Diatoma - 8,000 3,500 - 36,000 7,917 agila 1.000 32.000 16,556 - 48,000 9,333 Svnedra 3.000 42,000 16,000 - 87,000 17,167
- - - - 6,000 500 overboa - 5,000 2,111 - 3,000 333 Tabellari- - 6,000 667 - 51,000 4.250 Achnantheg - 1,000 111 - - -
Cosconei 5,000 45,000 22,000 1,000 24,000 11,667
- 26,000 4,778 - 12,000 2,667 Navicula 96,000 558,000 391,444 35,000 528,000 231,500 Pialaria - 11,000 1,500 - 6,000 583 Gomphonema - 1,000 111 - 3,000 250 Cvmbell - 39,000 11,833 - 24,000 6,833 8,000 119,000 43,444 3,000 122,000- 52,167 Cvmatot~legr~ ......
.rall - 5,000 2,000 - 24,000 7,833
.... -not. - 3,000 250 itarlli - 14.000 1,555 - - -
Pboicoschenia - 10,000 2,444 - 20,000 4,833 CyanophVta Coelosphaeriu - 1,000 111 - - -
ooccs .... - - - 4,000 583 Barimoveia ---
Gloeocavea- - - 4,000 667
.. n- - - 4,000 333 11nabva ......-
OnJii*itEiA - 3,000 444 - 14,000 2,250 Anabaena - 18.000 5,222 - 6,000 1.750 Aphanizomenon ---
Cvlindrospermum .... 4,000 333 ua.ia ...
- - - - 9,000 917 Total 147,000 3.351,000 1,366,383 68,000 3,115,000 832,915
(&)Densities of phytoplankton are listed as numbers of organisms per liter of water.
0 LGS ECIC TABLE 2.2-11 (Paqe 1 of 2)
PERIPHYTON PRODUCTION LISTED AS TOTAL BIOMASS--STANDING CROP (MG/DNR)
AND TOTAL EROEUCTIVITY RATES (MG/DM2/DAY-1) (1)
Stations Exposure Time
.... (Days)
S7262~ S77580 Dates mqdm&~! ma/du'z/dav--'
17 May 1973 7(t) 29.9 -C3) 8.8 24 May 14 78.9 7.00 34.7 3.70 6 Jun 27 5.0 -5.68C 4) 7.6 -2.08 14 Jun 8 2.6 3.7 21 Jun 15 21.8 2.74 22.2 2.64 28 Jun 22 19.2 -0.37 34.4 1.74 28 Jun 7 5.11 6.8 9 Jul 18 5.8 0.04 5.1 -0.16 16 Jul 25 40.4 4.94 39.2 4.87 16 Jul 7 26.8 20.8 24 Jul 15 57.7 3.86 20.0 -0.10 31 Jul 22 42.41 -2.19 24.0 0.57 31 Jul 7 19.2 11.5 6 Auq 14 23.5 0.61 9.6 -0.27 13 Auq 21 26.1 0.37 11.5 0.27 13 Auq 7 11.6 6.4 21 Auq 15 30.4 2.35 16.9 1.31 28 Aug 22 59.7 4.19 20.9 0.57 28 Auq 7 25.6 7.41 4 Sep 14 29.0 0.49 9.1 0.224 11 Sep 21 54.4 3.63 22.8 1.96 11 Sep 7 29.3 13.2
-(5) 10.2 -0.23 24 Sep 20 1 Cct 27 11.8 0.23 1 Oct 7 8.5 8.7 8 Oct 14 16.9 1.20 9.6 0.13 15 Oct 21 33.0 16.1 19.0 1.34 22 Oct 7 7.2 4.2 29 Oct 14 17.4 1.416 10.1 0.84 5 Nov 21 13.7 -0.03 8.9 -0.17 13 Dec 15 1.0 5.0 20 Dec 22 3.8 -0.03 3.2 -0.26
LGS EROL IA2UE 2.2-11 (Cont'd) (Page 2 of 2)
Stations Exposure Time S77260 S7750 Date (Days spa5 madm2l&ayt madmi. min/dm&/dav-r 30 Jan 1974 14 1.5 - -(i) -
6 Feb 21 4.7 0.23 - -
13 Feb 28 13.2 0.40 12 Mar 7 6.9 -. ..
19 Mar 14 20.7 1.97 - -
26 Mar 21 14.8 -0.42 - -
30 Apr 8 81.6 - - -
7 May 15 133.9 7.47 - -
141May 22 16.6 -8.38 - -
21 May 7 8.5 - - -
28 May 14 22.2 1.96 - -
4 Jun 21 23.9 0.12 - -
30-31(7) Jul 7 2.8 - 2.8 -
6-7 Auq 14 20.0 2.46 6.2 0.19 13-14 Auq 21 17.9 -0.15 18.7 0.89 27-28 Auq 7 1.0 - 3.9 -
3-4 Sep 14 13.3 1.75 73.8 9.96 10-11 Sep 21 72.4 4.22 78.9 0.36 24-25 Sep 7 1.7 - 0.2 -
1-2 Oct 14 2.5 0.10 3.4 0.45 8-9 Oct 21 4.0 0.11 9.3 0.84 16 Oct 7 1.0 - - -
23 Oct 14 2.9 0.30 30 Oct 21 3.4 0.004 - -
13 Nov 7 0.6 ....
20 Nov 14 5.2 0.65 - -
27 Nov 21 8.8 0.26 - -
'Values are listed as ash-free dry weights by station for 1973 and 1974, Schuylkill River, Limerick Generating Station.
2Tbis represents the actual number of days that the artificial plates are exposed to peripbytic growth from the date the samplers were set.
3 Dash indicates no values recorded because of low growth rate during the first seven (7) days of colonization during each sampling period.
4A neqative number for production rates indicates a sloughing of peripbyton biomass resulting from scourinq by high river flous.
$No values recorded due to loss cf Plexiqlas plates at station S77260.
'No samples were collected from this station except for peak growing season during July, Auqust, September, and early October.
?These stations were sampled cn twc (2) consecutive days. On the first date station S77580 was sampled while station S77260 was sampled on the followinq day.
LGS EROL TABLE 2.2-12 SPECIES LIST AND RELATIVE QUALITATIVE ABUNDANCE OF AQUATIC MACROPHYTES IN THE VICINITY OF LIMERICK GENERATING STATION Scientific Name Common Name Abundance (1)
Thallophyta Chlorophyceae Green algae Cladophora spp. A Bryophyta Musci Moss Fissidens sp. U Spermatophyta Najadaceae Curly-leafed pondweed Potamogeton crispus C P. berchtoldi Thin-leafed pondweed C Alismataceae Saggittaria latifolia Arrowhead R Hydrocharitaceae Elodea canadensis Waterweed R Lemnaceae Lemna minor Lesser duckweed U Pontederiaceae Heteranthera dubia Water stargrass A Onagraceae Jussiaea repens Creeping primrose willow U Haloragaceae Myriophyllum exalbescens Water milfoil A (1) A = abundant, C = common, U = uncommon, R = rare
LGS ERC 9 TABLk 2.2-13 (Paqe 1 of 3)
SPECIES LISI ANC PTLATIVE ABUNDANCE OF M4ACICINHERTEBRA¶ES COLLBIE.T BY ALL NETBCDS FGHM THE SCHUVIKILI RIVER, 1970-1976 ANNELIDA (cont'd) ARTHIRCECCA (conttd)
PORIFERA Hirudinea (cont'd)
SPonqillidael P2,253) l8ovoda (cont'dl Er pobdel I idae punctata (C,29) Leptophleblioae COELENHTZATA Er~obdella Lectophl.bja pp. (R,6)
HyAr a1 Opp. (1,9) gjUIMe (R,6)
PLJTHYHELZL INTHES HooreobdeslL ferviA (R.29) Paraleptopblebia Plaqiostomidae ARTHRO PODA argJcigg (0,19) Isopoda Baetidae Ulimz Planariidae Asellidae Eaes inteual1auis (C1,6) jaamia dorotowephalaI (R, 191 AselluU commi (C.34)
Lirceus up.2 (1,25) 3.j.lyat ivjwje (P,6) (1.6)
D. 119LLgj (C019) Amphipoda NEMERTEA Gammaridae Prostomf EXISQ2=g (C,12)
NENATODA (0,9) uimmar fasciatus (C,16) i.ooetbup (p, 6)
BRYOZOA f.ranoonyx agacili (A,16) a~vagnecte .LLziInj (C,17) Amletus lin tIM- (R,61 ANN a ID Decarpoda A. (R1,6)
Oliqocbaeta Cambaridae Pseudoclmeon Uyrsl-- (C,6)
C*P-baru bartonI (u, 151 Lumbricidae (U,21 Orcon~e~gM lio (c,151 Z.-dubrAykA (PI6) sUp. RIG6)
Tubificidae LnMQUAIMa nawuast inRJ (U,2) ,.Q. obscurs (U, 15)
(R Oydracarirna (U,25) 8p.
b- cervix (C,21 Siplonoridae Colleakola
- 16. bofmeinteri (A,21 Isotomidae I-. +/-uu zesL (0,2) ~P-. (UP 61 AXQblJ J2) 1od Iatoma Op.' (1U,331 Beptaqenildae Iaotomurus caluetrist (U,33) 2-mlt-estkns (A,21 Poduridae AtlDurX0
- g .Iermlelvl q- ZXMW.t#.UW(R,201 (u. 20)
PsamWA ryC tide .cauri.Ietomg Rou Jfguatig 1 (1,33) Stenonema gr A- tiDnc u (R,20)
(R.20) app.
8rM20+/-13U (R.2) Sminthuridee (1,331 Ava ir~luna llmQonobs (9,21 Ephemeroitera Stenongnsa IInSm (R, 201 Aeolosomtidaes (R,2 Ephemeridae I. lnteILII (1,.20) slaididae (0,21 0.- itha (1,20)
Lumbriculidae (A,2) 3. outtula (I,6) A.- Vull u (R,20)
Iiatukklux op. a 2.. gainguego mm (R,20)
A. l Jintulm (C,201 Polychaeta Caenidae (u,6) .No Devjtelly ( 1,20) s~n pp.
Uahanu lA gjou"a (0I26) 23. rutremao latm 1.20)
HLrudlnma gracbycerus (R,61 ru-r I (P,201 2gcrtbfso.,(c,61 Gloesiphonildae Ephemere llidae 2-- RMSMA5*LM, (R. 201 A ah (1,29)
(U,6)
Ephmanla dfi&eM up."
ea.3 1p.6)
A. fusc kksU tenl*(X,292 (1. 29) . attenuja (RI6) Odonata dort. (R1,61
_.aeutiv* 10,6) Gomphidae A. elonga I(,29) tpOMQg-pU$j§ 12kQ2_s (P. 23)
Pl. 1,IbJl~iA 1C.29) GRhu fraternu (1,23)
Lanthibu abietvlu8 R,23)
RDARillicz (R,29) L. earu11. (R,231 E. nari*li&ir (R.291 _J.sipl * (1*.6) agverour asogonwhu (R,231 Actino2della Irnniat (P,291 .erratoide. (RI,61(*, 6) .3ylYrm uvniSua (R,231 ji. cbEgdelgla ahak" (0,291 Llbellulidae Piscicolidae LStiniap.' (R,223)
- 1. 1xiblb(,23)
.1- vmjui fJin 21aLiJ Keduct (R.221 (0,6)
(0,.6)+
zobdell lutakaJ' (P.22)
Las EROL IABLE 2.2-13 (Cont'd) (Page 2 of 3)
ART'!iRCPOVP' (cont'di AR1TH3cpODA (cant *d) AftrTD3PODA (cofltod)
Coleoptera ilydropsycbidae Upbemeroptera (cont 'd) (,8 Ilacroniidae ilaliplidae Utcroi2E. allechininsoi (U. 23) Peltodyte duodecimpunctatuu (R,33) Adxrznvaxbe k,+/-+/-sn. (C'181 Calopteryqidae Dytiscidae i. halerati 06281 Ca.l22cflhz or. (U,9) &guabus (R,33) H.simiaaul~a (3,228)
HydrgQ.Vrus consimil I (R.331 sip. A (1,35) o.p. BI (R,351 Coenagricnidae Lacco2biluJ. pLQxi.Imus (3.33) 1j. op. C (Co35)
GyJinuw aliliI (3@8) hAri a p. (C,91 Hydrophil jdae o.p. 0 (0,35)
&nallaarui opp. (R,91 Mcrmaa L~reainu (C9331 u.
op 2 (3J35)
Ischnur ag1p. (11.9) I2~brus (R.33) p. Ft (3.351 s.
Aeschnidae Lacxqbwat (#333) ilydroPtilidae Wyoeria v4nosa (0,23) Hixk9Dbus!& (R,33)
Lestidae £cwydrpig (3.33) HzsXpatuata C, 28) teste 1 (R.9) U.nmata (3,28)
Plecoptera Hydrophilidae Taeniolpteryqidae M.LLa3idiu app. (R,331 MAN si~aM (3,281 Taeniovterv nivglis (3,31) Psephenidae 1i&gWicsbia &1&igiE'o (R.28)
JIZ.IIJh GP- (3@28)
- 2. mur~a (R,31) 0uinth ~squ. (1.281)
T. n*Xammi (3#31) Ia pidoptera Capniidae Dryopidao pyralididae A1J9g.aunI* (0,31) Z2MiUXUra.ti uP. (0,v33)
Hemour idae Plaidee Ancyron Dilptera Amwbinemuca, delgo (R,311 lai.L1IRi (P,3)
?ipuiidae Perlidae pubianki mittat. (C.3) jainungbI op. (,3331 11aucbupsx1 (R,311 meocegrla clymene (R,311 .9.guadrinctala (R,3)
M4icrocylloepuB cusiflIaa1 (R#3) 2icrnotb up.t (R,331 Rs~ti aI~ (0,311 !ggioserM1 tiixntatu (C, 3) fEJ2JJItPIU op. (0,33) jIjpj.)Ajj crna 413) tiel~nti RU(3.33)1op.
A. Lieuria, (3.31) (U31 gtonlJi3 opf). (C,3) fitmani app. (C@331
&. 51101na (R.311 gsimuliidoe A. lZD1Sign (3,31) Chrysomelidae A. asnza (3,31) Galergcella1 (0,33) .Uplmiia rJ.Utgu (U,30)
-Inichoptera chironomidae Periodida* Glossouomatidae Giossogg" a;. (3.28) IXQ1JU~a z22r31 (A.21)
Pyaccphilidae ~~1aeuwwa aiiisnla C,31)
Chloropenlidae BbyacoRbil& aMias 0,28) pentaneunini p. A21)
Philopotamidae Gegridas chbimagra obsus311 (0,28) Taraytaruifli orPp. (A#21)
.C. aterma (0,28) chiLLI2o!rm suppo fc,211 Corixidiae worma1ld rNgsu' (1 ,26) cb1L9D235I app. (CI.271 oin Irigog~2rizat (R,33) _W.shaikne.It (3.28) 2Kik u.1 op., (U.21)
Silga" (Pv3.33) Psychouyiidae 91RI4i2 P. (0.277 uyesv 14eqalopt era 1ux3.bgmui (Rol1) gIyE&.ttendiveg sp. (0. 21)
Sialidae clvlcenlro a.U3 3emo(R028) P '1-~I1 gupp. (0,21)
Iijn) op. (C,32) izuarecinviBn Sq. 11429), t~it 2+/-Stenj 1 20 app. (u,.21)
Corvda lidae Limnephilidae
.geohyJax op.$ (3,32) FIAra-ailterborfiiella up. *(92119 Chauljods op.& (3,32) 2rxorydalu cQn~iati (0.321 Leptoceridae Larten d&Mrf~ t1GP . ( 3@21) iju~goni jr t~coris (0, 32) Ceraclea op. A (3.28)
Neuroptera Oeratis app. 10.38)
Sieynidae Hysg.acid spu g1u~axlin (R,281 karachixonamu1 SP- (021) fiiAijra viggrig I (R.331 TriL01ngd op. (3,28) Phaenoivac~tra ON (C#21) 91.3g~kF areolaris 10.11
0 0 LGS EIOL TABLE 2.2-13 (Cont'd) (Page 3 of 31 ARTHAP0ODA (cont d) AIBROPODA (cont 'd) NOLLOSCA Diptera (cont'd) Ciptera (cont*d) Gastropoda ZDXIr91L op. (0,21) Beleidae Ppbysidae LaJsoajaej*a up. (R927) ka.JnX1.A OPP. (U, 33) PZbiu bet&er9UkK2Dh (1.24)
Daresa op. (0,21) tiloezz*J*a op.&t (1,33) -. sayjL (3,13)
C8lole p..& (R, 33)
Prodjameea olivace (R,27) Lymnaeidao Cardiocladius obscurus (U,27) Empididae Lxuaau iamiLi (U,13)
Crctou ic inct u8(A,21) Type A (0,35) Planorbidae Cther Crijotog9 supp. (C*21) Type 8 (C,35)
Orhcadius sp. (C.21) Ephydridae Menetys op. (3,13) opp. (U.27) aukiefferiell BraChydeutera agentatai (R,33) floinet&U1 exauou (3,13)
Scatella-Neoacatella op.& (3.331 MliEom trii (R, 13)
Trichocladiu op. (U,21) JI. anceps (A, 13)
Trissocladius op. (R,21) Culicidae ChaobWu op.& (0,33) Ancylidae P8ectrocladius op. (0,21) Ahees' (31,33) Egrrissia tnar (A,13) op. (0,211 8rilli Culex op.' (3,33) Pleuroceri dae Seittia app. (R,21) Linsp op.' (R,33) Goni1bglJ (A,13)
Nycetophilidae (R,33) Ilydrobiidae n op. (3*21) DolichopodLdae o noneur op. (P,27) J~lX9*Sg.UA(R,331 Amni2g1 liaam (, 13)
Ihtenemannele8 ~op. (R,21) lelocypoda Psychodidae Takanldae Ophaerildae Pgvchoda op. (C, 18) Cryi.soL op. (V,33) BUUJJJulu 0,51 j1. altersnat (U,18) Ta.anus op. (P,33) .§. striatipus (A,5)
Pe1ccapI op. 0i(,18) Stratiomyiidae (R,37) Piajdiupup. (A,5)
Xg*l~matgjg2 &Ibj~ungjat (C,18) lalia (3,33) Unionidae Rbaqionidae ZAEll~ti comunana~tnu (R#,7)
.Aber. varieuataI (R,33) AlaJmi]d
- uop.' (R,.)
Pboridae I&MmLggn" zn su ii OR, 41 DJilneDL3r. m, ta (3.33) ktbbyomiidan UJannnmJ*I* u u ifrDs' (9,331 Taxa or species not collected by cylinder uamFlers (the primary quantitative gear).
(t) A a abundant, C - common, U - uncommon, R W rare.
(a) Numbers refer to the taxonomic references listed below. For complete citations, see the Literature Cited section.
- 1. Boesel (Ref 2.2-17) 13. Harman and Berg (Ref 2.2-28) 25. Pennak (Ref 2.2-37)
- 2. Brinkhurst (Ref 2.2-18) 14. Hitchcock (Ref 2.2-29) 26. Pettibone (pers. comm.)
- 3. Brown (Ref 2.2-19) 15. Hobbs (Ref 2.2-30) 27. Roback (Ref 2.2-38)
- 4. Burch (Ref 2.2-20) 16. Holsinger (Ref 2.2-31) 28. Rose (Ref 2.2-39)
- 5. Burch (Ref 2.2-213 17. Holsinqer (peru. comm.) 29. Sawyer (Ref 2.2-40)
- 6. Bruka (Ref 2.2-22) 16. Jobannesen (Ref 2.2-32) 30. Stone (Ref 2.2-413
- 7. Clarke and Berq (Ref 2.2-23) 19. Renk (pets. comm.) 31. Burdick and Kim (Ref 2.2-42)
- 8. Dillon and Dillon (Ref 2.2-24) 20. Lewis Ref 2.2-33) 32. Tarter (Ref 2.2-43)
- 9. Edmondson (Ref 2.2-251 21. Mason (Pef 2.2-34) 33. Usinger (Ref 2.2-44)
- 10. Flint (Ref 2.2-26) 22. Meyer (Ref 2.2-351 34. William (Ref 2.2-45)
- 11. Flint (Ref 2.2-27) 23. Needham and Westfall (Ref 2.2-36) 35. Consultant's Designator 12.Gibson (peru. come.) 24. Farodix (pers. cows.)
0 LGS EROL Page 1 of 3 TABLE 2.2-14 NUMERICAL
SUMMARY
DATA ON IMPORTANT SPECIES (TAXA)(1) OF BENTHIC MACROINVERTEBRATES COLLECTED IN QUANTITATIVE SAMPLES (1972-1976) FROM THE SCHUYLKILL RIVER 1972 1973 1974 1975 1976 2 2 Taxon No./m % FO % No./m % FO % No./m 2 % FO % No./m 2 % FO % No./m 2 % FO %
Station 126.3 (2) 46.9 1.7 (2) 6.3 22.2 (2) 27.1 13.4 (2) 27.3 20.5 (2) 35.4 S76760 104.1 (2) 29.5 3 (2) 13.6 5.5 (2) 22.9 S75770 332 3.9 32.1 5.1 2 10.4 4.8 2 8.3 21.2 2 31.8 Prostoma graecense S O786n20 152.7 () 34.4 91.7 36.4 31.8 (2) 29.2 S76760 98.4 2 27.3 4184 4.1 2
(2) 18.8 8.3 1
15
(
(2) 1 16.7 13 ~ 2 20.5 11.3 2 10.4 S75770 446.7 5.3 39.3 33.2 (2) 18.2 Tublficldae S78620 345.8 2.4 43.8 1323.8 16.3 87.5 381.1 3.7 89.6 924 7.8 100 279.4 2.4 100 S76760 3123.8 50.5 90.9 3805 63.9 100 1850.8 24.2 100 3180.7 31.2 100 1960 32.4 100 S75770 3404.6 40 100 2191.6 39.1 93.8 647.2 12.9 91.7 - - - 1898.3 30.3 100 Erpobdel la punctata S78620- 1.5 (2) 9.4 15 (2) 33.3 15.4 (2) 20.8 10.4 (2) 36.4 3.8 (2) 20.8 S76760 3.7 12l 11.4 7 (22) 22.9 7.8 (2) 25 19.7 (2) 47.7 5.8 (2) 25 2.3 2 10.7 44 M2 20.8 1.7 (2) 10.4 10.4 (2) 31.8 S75770 Crangonyx gracilis 40 (2) 35.4 157.4 (2) 52.1 248.1 2.1 84.1 185.8 (2) 77.1 316.6 5.2 75 S76760 8.9 (2) 11.4 32.4 2 31.3 63.5 (2) 55 288.7 2.8 88.6 431.4 6.9 72.7 S75770 4.1 (2) 10.7 15.7 (2) 29.2 30.1 (2) 52.1 - - -
Cambarus bartoni 575bZ0 0.3 (2) 2.1 1.4 (2) 6.3 2.1 0.4 (2) 2.3 0.3 (2) 2.1 576760 0.7 (2) 4.5 0.3 (2) 2.3 0.7 (2) 2.1 0.4 (2)
S75770 Orconectes 3796u0 0.5 (2) 3.1 - 1 (2) 6.3 0.4 (2) 2.3 1.7 (2) 10.4 1.4 (2) 8.3 S76760 0.4 (2) 2.3 1 (2) 6.3 2 (2) 12.5 4.1 (2) 15.9 (2) 9.1 1.1 (2) 10.4 - - - 1.5 S75770 Aria(nymph) - - - 0.7 (2) 4.2 620 0.3 (2f 3.1 20.5 (2) 33.3 47.5 (2) 60.4 17.9 (2 45.5 62.5 ý2) 41.7 S76760 0.4 2.3 18.8 (2) 18.8 43 (2 42.5 65.6 (2 47.7 24.2 2) 39.6 84.9 (2) 52.3 S75770 - - - 13.3 (2) 12.5 71.4 (2) 56.3 - - -
Chuatopsyhe (larvae) 2513 21.8 100 576a0e 24.1 (2) 37.5 215.8 2.7 64.6 1353.5 13.0 95.8 1574.5 13.3 100 53.3 (2) 60.4 S76760 2.5 (2) 15.9 5.1 (2) 20.8 46.7 (2) 45 161.3 (2) 72.7 (2) 63.6 43.8 - 49.2 S75770 1.2 (2) 7.1 2 (2) 12.5 61.5 (2) - -
Cheumatopsyche (pupae) 0.7 (2) 4.2 S78620 Z - . 2.2 (2) 6.8 0.3 (2) 2.1 S76760 .... 0.7 (2) 4.5 S75770 - - -
LGS EROL Page 2 of 3 TABLE 2.2-14 (Cont'd) 1972 1973 1974 1975 1976 Taxon No./M2 % FO % No./m 2 % FO % No./m 2 % FO % No./M 2 % FO % No./m 2 % FO %
Station Hydropsyche phalerata (larvae)
S7862 3.2 (2) 9.4 - - - 14.3 (2) 39.6 837.6 7.1 88.6 196 (2) 85.4 576760 0.2 (2) 2.3 - - - 2.5 (2) 7.5 93.1 (2) 63.6 31.1 (2) 52.1 575770 - - - - - - 2.4 (2) 12.5 - - - 27.6 (2) 40.9 Chironomidae (larvae)
S78620 1503.8 10.3 96.9 4378.1 54 97.9 5289.3 50.8 97.9 4690 39.5 97.7 3730.2 32.3 97.9 S76760 1764.4 28.6 95.5 1402.7 23.5 95.8 1063.5 13.9 97.5 1504.5 14.8 90.9 1154.7 19.1 97.9 S75770 1271.2 27.9 82.1 1873.6 33.4 87.5 976.8 19.4 95.8 - - - 1125.6 17.9 100 Chironomldae (pupae)
S78620 88.8 (2) 65.6 121.9 (2) 43.8 59.8 (2) 52.1 44.3 (2) 38.6 88.5 (2) 27.1 S76760 110 (2) 63.6 28 (2) 35.4 16.4 (2) 27.5 67.4 (2) 36.4 24.2 (2) 41.7 S75770 53.5 (2) 42.9 71 (2) 31.3 6.8 (2) 14.6 - - - 19.7 (2) 22.7
"* U*'U 10037.2 68.5 56.3 1148.6 14.2 89.6 611.7 5.9 89.6 60.7 (2) 65.9 300.5 2.6 64.6 S76760 403 6.5 45.5 102.5 (2) 50 207 2.7 75 26.5 (2) 36.4 13.7 (2) 37.5 S75770 1044.5 12.3 67.9 174.9 3.1 70.8 367.5 7.3 77.1 - - - 29.8 (2) 54.5 Helisoma anceps.
' 495.9 3.4 37.5 263 3.2 77.1 654.7 6.3 85.4 247.4 2.1 40.9 1 (2 2.1 576760 11.3 (2) 29.5 4.1 (2) 14.6 20.5 (2) 45 6 (2) 18.2 0.7 (2) 4.2 575770 140.5 (2) 75 10.2 (2) 39.6 20.8 (2) 39.6 - - - 0.4 (2) 2.3 Ferrissia tarda 375B9O 514.7 3.5 59.4 71 (2) 50 77.5 (2) 37.5 13 (2) 31.8 270.8 2.3 52.1 576760 293.6 4.8 38.6 36.9 (2) 39.6 59 (2) 27.5 2.2 (2) 11.4 4.1 (2) 12.5 S75770 virginica Goniobasts 258.8 . 71.4 51.9 (2) 47.9 45.4 (2) 20.8 - - 2.6 (2) 13.6
- 1. 0 211. 0 onoasi 3.1 (2) 15.6 17.1 (2) 35.4 1158.8 11.1 93.8 2095.8 17.6 100 2221 19.3 100 S76760 4.5 (2) 13.6 378.4 6.4 39.6 4056.6 53 100 4323.8 42.4 100 2011.3 33.2 100 S75770 63.2 2 57.1 1051.9 18.7 95.8 2279.7 45.3 100 - - - 1565.9 25 100 P1sidium s-wo 84 (2) 25 75.1 (2) 52.1 23.6 (2) 43.8 394.9 3.3 100 713.8 6.2 64.6 576760 3.8 (2) .15.9 4.1 (2) 16.7 9.8 (2) 25 193 (2) 61.4 166.7 2.8 35.4 S75770 21.1 (2) 39.3 5.5 (2) 18.8 32.8 (2) 50 - - 396.4 6.3 63.6 Sphaerium 4.6 89.6 S78620 1130.1 7.7 43.8 214.1 2.6 79.2 324.1 3.1 62.5 236.2 (2) 90.9 533.8 87.4 (2) 70.8 576760 41.5 (2) 45.5 10.2 (2) 18.8 85.7 (2) 50 17.9 (2) 31.8- 3.1 93.2 302.3 6 70.8 - - - 196 575770 282.8 3.3 92.9 32.1 (2) 54.2
LGS EROL Page 3 of 3 TABLE 2.2-14 (Cont'd) 1972 1973 1974 1975 1976 Taxon No./m 2 % FO % No./M2 % FO % No./M 2 % FO % No./m 2 % FO % No./m 2 FO %
All Others S78620 145 (2) 191.9 2.4 213.5 2 373 3.1 379.1 3.3 576760 204.6 3.3 102.5 (2) 113.9 (2) 215 2.1 186.1 3.1 575770 82.6 (2) 102.1 (2) 167 3.3 375.6 6 Annual Mean S78620 14656.9 8100.4 10419.7 11875.6 11535.2 S76760 6179.7 5958.0 7650.4 10185.9 6058.7 S75770 8508.8 5610.3 5035.5 6270.9
( 1 )For each species, or taxon, the following parameters are given by station for each year: mean number per square meter,
)percent of composition (%), and frequency of occurrence (FO %).
(2 Less than 2%.
IGS EROT TABLE 2.2-15 (Page 1 of 2)
BIOMASS( 1) OF IMPOITANT BENTHIC 1ACRCINVERTEBRATES COLLECTED IN QUANTITATIVE SAMPLES (1972-1974) FROM THE SCHUYLKILL RIVER 1972 1912 19714 Biomass % Biomaes Taxcm __J_ 1i S78620 27.4 (E) (a) 6.5 (2) 0.3 876760 211.8 1.4 (a) (2) 0.14 S75770 94.7 2.5 1.1 (a) 0.9 (2)
Prostoma araecense S78620 13.11 (a) (2) 1.5 516760 11.6 (a) 2.0 (E) (2) 575770 411.0 (2,)
1.2 0.4 1.0 Tubificidae S78620 61.8 (2) 218.8 4.1 2811.3 1.8 576760 1484.9 28.0 572.7 8.0 988.9 2.8 575770 1020.7 27. 1 463.0 4.1 361.9 1.2 robdella 2Ui=aa s78620 113.3 (2) 313.8 5.9 223.9 1.11 576760 151.4 8.7 1714.8 2.5 1146.9 (2)
S75770 92.9 2.5 175.0 1.6 116.1 (2)
Crnagnnyx OrAclul 578620 16.9 (a) 51.1 (a)
S76760 5.3 (a) 14.7 (a) 26.9 (2) (a) 575770 2.2 6.9 9.9 (a)
Cambaru8 .hartoni 878620 1.2 (a) 576760 296.6 17.1 5.7 (a) 875770 327.2 1.1 Orconectes 578620 800.1 8.6 402.7 2.6 s76760 1110.7 8.1 350.1 8411.0 2.11 575770 2319.5 7. 8 242.5 2.2 (2)
Argia (Nymph) 578620 1. 1 (a) 26.5 (a) 50.2 (2)
(2) (a) 576760 0.3 23.5 19.3 (2)
(2) (2) 875770 16.5 74.2 Cbeumatopsyche (Larvae) S78620 35.9 (2) 155.8 2.9 638.5 11.1 (2) 576760 3.9 (2) 3.5 (2) 25.0 (2) (2*)
575770 0.3 (2) 1.8 16.2 Hydropsvcbe phalerata (Larvae) 578620 3.5 (2) 10.0 (2) 076760 0.11 (2) 1.3 575770 2.0 Cbironomidae (Larvae) 578620 58.8 (2) 266.6 5.0 272.5 1.7 (2) 576760 127.0 7.3 94.4 1.2 60.9 (2) 575770 103.2 2.7 138.2 1.2 62.6
LGS EROL TABLE 2. 2-15 (Cont'd) (Page 2 of 2) 1972 1972 1974 Taxon Rioma~s !-
-- Biomass Chironomidae (Pupae) S78620 6.8 (2) 11.0 (2) 6.9 (2) (2) 876760 9.7 2.2 1.6 Ca) (a) (2) 875770 4.3 4.8 0.7 Pbij inteqra S78620 5494.1 58.7 2022.2 38.1 859.8 5.5 876760 227.3 13.1 220.9 3.1 313.1 (2) 875770 825.1 21.9 299.4 2.7 421.5 1.4 Helisoma anceps 878620 1891.1 20.2 1527.8 28.8 2646.6 16.9 876760 41.1 2.4 44.7 (2) 99.7 (2)
(2) (2) 875770 764.6 20.3 63.7 131.8 Ferrissia tarda (2) (2)
S78620 98.9 1.1 16.6 16.7 (2) (2) 876760 58.6 3.4 6.6 11.8 (2) 875770 45.8 1.2 11.1 7.4 C()
Goniobasis v ini 878620 4.4 (2) 75.4 1.4 9595.1 61.2 876760 17.5 1.0 5419.8 76.0 32198.2 90.9 875770 299.4 8.0 9491.4 84.6 25336.8 84.7 Pisidium S78620 11.2 (2) 19.8 (2) 4.9 (2)
(2) 876760 2.7 (2) 3.3 1.6 (2)
(2) 875770 6.3 (a) 1.8 6.6 (2)
Sphaerium 878620 565.2 6.0 193.1 3.6 182.4 1.2 876760 21.0 1.2 12.4 (2) 49.2 (2)
S75770 76.2 2.0 25.6 (2) 129.4 (2)
All Others 878620 236.1 2.5 440.7 8.3 431.2 2.7 876760 106.5 6.2 178.1 2.5 648.5 1.8 875770 380.1 10.1 282.3 2.5 660.3 2.2 Annual Mean (q/Sm) 878620( )(') 9.4 5.3 15.7 876760(33(4) 1.7 7.1 35.4 875770(4) 3.8 11.2 29.9 (1) Mean biomass (milliqrams per square meter) and percent composition (S).
(2) Less than 1%.
(3) Annual mean biomass in 1975 at S78620 and S76760 was 18.8 and 37.1, respectively.
No samples were collected at 575770.
(4) Annual mean biomass in 1976 at S78620, S76760, and 875770 was 22.7, 25.1, and 24.7. respectively.
LGS EROL Page 1 of 7 TABLE 2.2-16 MONTHLY DENSITIES (MEAN NUMBER PER SQUARE METER) OF IMPORTANT SPECIES (TAXA)
OF BENTHIC MACROINVERTEBRATES COLLECTED FROM THE SCHUYLKILL RIVER, 1972 THROUGH 1976 Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec 1972 - - - - 32.8 1836.1 454.9 1973 8.2 - 16.4 4.1 32.8 - - -
1974 - - - - - - 8.2 36.9 - 12.3 1976 - 4.1 - 12.3 61.5 4.1 8.2 106.2 36.9 -
S76760 1972 8.1 2.7 2.7 - - - 16.4 1028.7 65.6 20.5 1973 - - - - 4.1 - - -
1974 .-.. 4.1 8.2 - 4.1 -
1975 - - 4.1 - 4.1 12.3 - - 12.3 1976 4.1 -.- - 16.4 12.3 32.8 -
S78620 1972 5.4 29.6 .- - 446.7 467.2 61.5 1973 - - - 8.2 12.3 - - - - - -
1974 - - - 4.1 12.3 90.2 102.5 24.6 24.6 8.2 1975 - 57.4 - 12.3 32.8 12.3 16.4 8.2 - -
1976 - -- - 8.2 32.8 82 49.2 61.5 12.3 Prostoma graecense 57577o 1972 - - - - 963.1 2123 41 1973 36.9 -- - - .- 12.3 1974 - - - - 49.2 90.2 41 1976 - . . - - - - 184.4 180.3 -
S76760 1972 - - - - - 627 413.9 41 1973 - - - - 4.1 - 131.1 86.1 -
1975 - - - 77.9 ...- - 57.4 - 8.2 1976 - - - - - 4.1 131.1 - -
S78620 1972 - - - - - 172.1 360.7 651.6 36.9 1973 - - - - 4.1 - 24.6 - - -
1974 - 20.5 - 4.1 - - 4.1 - - 20.5 41 82 1975 - 24.6 - 4.1 - - - 36.1 541 57.4 45.1 20.5 - - 184.4 4.1 - - 4.1 94.3 73.8 -
1976 -
Tubificidae S75770 1972 - - - - 1086.1 - 11873.9 4397.5 4598.4 291 623 963.1 1973 1045.1 36.9 520.5 803.5 5319.7 14897.5 2028.7 344.3 1151.6 32.8 110.7 8.2 1974 459 - 106.6 495.9 274.6 811.5 3803.3 700.8 127 102.5 430.3 299.2 155.7 1976 - .571.5 493.2 409.8 965.8 129.5 784.2 579.9 864.8 907.8 717.2 239.1 S76760 37.6 357.5 10.8 185.5 - 5934.4 1122.8 3430.3 4635.2 1196.7 1245.9 6127 1972 41 1973 2614.8 721.3 623 2573.8 10090.2 20532.8 4700.8 590.2 1147.5 1750 274.6 516.4 1053.3 3434.4 4495.9 3364.8 516.4 102.5 - 873 -
1974 979.5 3172.1
- 4848.4 5532.8 1901.6 1877 2897.5 6938.5 1250 1065.6 3278.7 4106.6 1291 1975 848.4 1976 "229.5 214.5 219.3 2450.8 1104.5 1846.3 637.3 545.1 429 526.6 2350.4
LGS EROL Page 2 of 7 TABLE 2.2-16 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Tubificidae (Cont'd)
S78620 1972 623 1291 340.2 754.1 831.1 1973 127 364.8 274.6 1754.1 8163.9 3942.6 163.9 233.6 69.7 155.7 12.3 1974 221.3 979.5 323.8 94.3 791 1524.6 118.9 12.3 24.6 82 36.9 364.8 1975 553.3 196.7 286.9 750 3717.2 1348.4 1836.1 635.2 295.1 311.5 233.6 1976 32.8 53.3 35.5 49.2 526.6 327.9 217.2 217.2 26.6 110.7 98.4 114.8 CgracilIs 1972 20.5 8.2 1973 4.1 - 4.1 - 32.8 12.3 28.7 61.5 - 45.1 1974 8.2 16.4 28.7 12.3 8.2 53.3 20.5 53.3 53.3 20.5 82 4.1 1976 - 463.1 28.76 32.8 82 2274.6 881.1 536.9 98.4 163.9 106.6 77.9 S76760 1972 16.4 73.8 8.2 1973 20.5 4.1 20.5 69.7 16.4 143.4 16.4 98.4 1974 12.3 24.6 16.4 36.9 356.6 86.1 49.2 4.1 49.2 1975 323.8 377 135.2 926.2 344.3 229.5 102.5 45.1 229.5 163.9 299.2 1976 41 4.1 20.5 364.8 41 565.6 323.8 803.3 229.5 381.1 274.6 750 S78620 1973 4.1 28.7 16.4 45.1 57.4 286.9 24.6 16.4 1974 4.1 28.7 61.5 61.5 606.6 8.2 20.5 20.5 8.2 836.1 233.6 1975 176.2 8.2 45.1 262.3 913.9 344.3 315.6 434.4 86.1 65.6 77.9 1976 16.4 16.4 16.4 65.6 8.2 979.5 209 123 315.6 131.1 262.3 86.1 Cambarus bartoni S75770 1974 8.2 1976 4.1 S76760 1972 8.2 4.1 1973 1975 4.1 1976 - 4.1 S78620 1973 - 4.1 1976 - 8.2 4.1 4.1 Orconectes spp.
S75770 1973 4.1 4.1 4.1 4.1 4.1 8.2 1974 1976 4.1 4.1 4.1 4.1 S76760 4.1 1972 4.1 1973 8.2 4.1 12.3 4.1 1974 1975 6.1 20.5 8.2 4.1 1976 8.2 4.1 4.1
LGS EROL Page 3 of 7 TABLE 2.2-16 (Cont'd)
Taxon Station Year Jan Feb Mar Apr pay Jun Jul Aug Sep Oct Nov Dec Orconectes (Cont'd)
S78620 1972 4.1 4.1 1974 4.1 4.1 1975 4.1 4.1 1976 4.1 4.1 4.1 4.1 Argia spp.
~S75770 1973 - 123.9 - 24.6 12.3 1974 12.3 4.1 12.3 4.1 8.2 4.1 53.3 250 209.9 229.5 69.7 1976 8.2 4.1 4.1 73.8 454.9 225.4 45.1 118.9 S76760 1972 4.1 -
1973 4.1 53.3 - 131.1 36.9 1974 8.2 24.6 4.1 4.1 12.3 8.2 209 118.9 - 65.6 1975 61.5 8.2 4.1 32.8 459 86.1 16.4 28.7 1976 4.1 8.2 8.2 57.4 114.8 45.1 41.9 12.3 S78620 1972 2.7 1973 24.6 118.9 45.1 45.1 12.3 1974 4.1 12.3 4.1 12.3 8.2 28.7 4.1 65.6 213.1 135.2 36.9 45.1 1975 32.8 4.1 36.9 53.3 36.9 24.6 8.2 1976 4.1 4.1 4.1 69.7 385.2 163.9 106.6 12.3 Cheumatopscche spp.
$5770l 1972 8.2 1973 4.1 - 4.1 4.1 - 4.1 8.2 1974 8.2 32.8 4.1 4.1 12.3 16.4 151.6 352.5 155.7 1976 - 245.9 114.8 32.8 6.1 - 32.8 16.4 4.1 12.3 16.4 61.5 S76760 1972 8.1 2.7 8.1 - 4.1 - 4.1 4.1 4.1 8.2 16.4 4.1 16.4 8.2 1973 1974 49.2 16.4 16.4 4.1 - 8.2 24.6 348.4 1975 53.3 151.6 41 41 131.1 49.2 139.3 491.8 479.5 131.1 65.6 1976 69.7 41 24.6 4.1 49.2 20.5 32.8 106.6 53.3 82 53.3 73.8 S78620 75.3 102.2 2.7 4.1 8.2 1972 1973 8.2 20.5 12.3 8.2 45.1 8.2 610.7 602.5 643.4 631.1 139.3 200.8 8.2 143.4 28.7 692.6 2266.4 6332 1848.4 3053.3 864.8 663.9 1974 1975 467.2 127 401.6 200.8 1045.1 698.8 2405.7 6741.8 1618.9 1405.7 487.7 1976 115.7 188.5 258.2 106.6 43 1229.5 6151.6 3172.1 3651.6 6471.3 3979.5 1061.5
LGS EROL Page 4 of 7 TABLE 2.2-16 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Hydropsyche phalerata S75770 1974 8.2 - - 4.1 8.2 8.2 1976 - 123 102.5 24.6 4.1 4.1 12.3 20.5 12.3 S76760 1972 2.7 1974 24.6 1975 41 4.1 8.2 53.3/ 24.6 151.6 245.9 327.9 135.2 32.8 1976 41 8.2 8.2 12.3 24.6 45.1 69.7 57.4 49.2 57.4 S78620 1972 21.5 4.1 1974 4.1 - 4.1 20.5 28.7 41 45.1 28.7 1975 20.5 53.3 45.1 807.4 532.8 1799.2 3532.8 1032.8 1147.5 241.8 1976 180.3 86.1 41 - 397.5 57.4 274.6 348.4 319.7 368.9 188.5 Chi ronomldae (larvae)
S75770 1972 - 3500 36.9 2803.3 3364.8 733.8 159.8 1973 127 16.4 725.4 459 1864.8 7209 1028.7 1623 9192.6 4.1 135.2 98.4 163.9 155.7 12.3 57.4 827.9 2188.5 1974 979.5 450.8 2733.6 1397.5 918 1836.1 1976 377 614.8 1069.7 3504.1 1557.4 2557.4 1131.1 934.4 188.5 159.8 286.9 S76760 1972 322.6 190.9 2021. 5 2241.9 2967.2 36.9 3356.6 5233.6 2454.9 418 163.9 1973 422.1 422.1 643.4 1409.8 467.2 4893.4 3196.7 1344.3 3569.7 98.4 139.3 225.4 1974 1024.6 254.1 2754.1 1110.7 2586.1 2135.2 332 176.2 16.4 245.9 1975 2397.5 2528.7 2582 3032.8 1741.8 1922.1 2036.9 86.1 143.4 20.5 57.4 1976 278.7 90.2 139.3 1360.7 1172.1 2573.8 3135.2 1258.2 2598.4 532.8 299.2 418 S78620 1972 86 414 169.4 3176.2 2840.2 2811.5 1627 905.7 1973 647.5 881.1 3172.1 12016.4 11024.6 4725.4 3959 1282.8 12180.3 1012.3 733.6 901.6 1974 713.1 4057.4 20889.3 6553.3 6946.7 8143.4 3065.6 24.6 61.5 1450.8 1327.9 10237.7 1975 9782.8 4274.6 14491.8 4684.4 4786.9 6766.4 4274.6 1991.8 373 90.2 73.8 1976 442.6 803.3 1961.7 16475.4 11004.1 4344.3 5086.1 1213.1 1500 696.7 983.6 741.8 Chi ronomidae (pupae)
S75770 1972 - 114.8 - 204.9 41 8.2 4.1 1973 8.2 57.4 590.2 8.2 8.2 180.3 1974 4.1 4.1 - 28.7 20.5 24.6 1976 45.1 118.9 20.5 28.7 4.1 S76760 1972 21.5 10.8 104.8 610.2 24.6 176.2 147.5 114.8 1973 36.9 20.5 118.9 49.2 8.2 102.5 1974 45.1 57.4 57.4 4.1 1975 16.4 16.4 82 16.4 4.1 73.8 532.8 4.1 49.2 49.2 110.7 28.7 4.1 32.8 4.1 4.1 4.1 1976
LGS EROL Page 5 of 7 TABLE 2.2-16 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Chlronomidae (pupae) (Cont'd) 1972 13.4 10.8 - - 153.2 106.6 - 90.2 336.1 - -
1974 - - 8.2 332 323.8 131.1 - 8.2 495.9 151.6 12.3 -
1975 - 28.7 77.9 168 123 135.2 12.3 - - 143.4 20.5 8.2 1976 4.1 - 28.7 684.4 278.7 - 28.7 12.3 12.3 - 8.2 4.1 1972 - - - - 4.1 - 8.2 20.5 307.4 3721.3 1852.5 1397.5 1973 467.2 155.7 217.2 45.1 12.3 172.1 16.4 - 69;7 57.4 32.8 852.5 1974 545.1 73.8 401.6 16.4 4.1 143.4 65.6 286.9 131.1 94.3 2577.9 69.7 1976 - 20.5 - - 16.4 36.9 24.6 4.1 8.2 135.2 45.1 36.9 S76760 1972 - 2.7 - - - 20.5 - 4.1 311.5 2528.7 1049.2 516.4 1973 217.2 102.5 16.4 20.5 - 8.2 4.1 - 102.5 - 299.2 459 1974 225.4 65.6 12.3 16.4 32.8 229.5 196.7 1106.6 - - 184.4 -
1975 - 32.8 28.7 - - - 16.4 53.3 77.9 45.1 36.9 1976 8.2 - - 4.1 4.1 12.3 4.1 45.1 61.5 20.5 4.1 S78620 1972 - 2.7 - - - 32.8 - - 11176.2 24172.1 30635.2 14278.7 1973 2106.6 1311.6 655.7 192.6 1024.6 401.6 4.1 8.2 3471.3 704.9 1602.5 2299.2 1974 307.4 672.1 82 131.1 12.3 848.4 2868.9 1930.3 82 168 114.8 123 1975 - 176.2 73.8 24.6 16.4 - - 4.1 151.6 123 82 16.4 1976 20.5 4.1 4.1 - - 28.7 508.2 82 844.3 1471.3 327.9 315.6 Helisoma ancepts 51sbzO0 1972 - - - - 184.4 - - 4.1 61.5 274.6 299.2 159.8 1973 32.8 12.3 12.3 16.4 - 8.2 4.1 4.1 16.4 - 12.3 4.1 1974 4.1 4.1 4.1 4.1 - - 98.4 69.7 16.4 4.1 20.5 24.6 1976 - - - - - 4.1 S76760 1972 2.7 2.7 - - - 12.3 8.2 - - 45.1 28.7 24.6 1973 - 24.6 4.1 - 4.1 - - - 8.2 8.2 1974 4.1 12.3 4.1 - - 45.1 32.8 28.7 - - 77.9 -
1975 - 36.9 20.5 4.1 4.1 - - - -
1976 - - - - 4.1 4.1 S78620 1972 - - - - - - - - 463.1 2057.4 1446.7 1973 721.3 590.2 799.2 598.4 57.4 4.1 - - 110.7 77.9 41 155.7 1974 65.6 49.2 16.4 12.3 4.1 106.6 868.9 4364.8 811.5 245.9 356.6 954.9 528.7 1024.6 1053.3 86.1 28.7 - - - - -
1975 -
1976 - - - - - 12.3
S LGS EROL Page 6 of 7 TABLE 2.2-16 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Ferrissla tarda S75770 1972 16.4 4.1 311.5 24.6 422.1 713.1 319.7 1973 147.5 73.8 36.9 24.6 16.4 151.6 4.1 20.5 147.5 1974 73.8 4.1 434.4 20.5 12.3 1976 16.4 - 4.1 8.2 S76760 1972 8.2 163.9 1860.7 803.3 303.4 1973 57.4 65.6 69.7 12.3 - 94.3 12.3 131.1 1974 188.5 4.1 12.3 12.3 237.7 135.2 1976 4.1 4.1 - 4.1 4.1 8.2 S78620 1972 2.7 8.1 885.2 877 1659.8 684.4 1973 217.2 498.2 73.8 94.3 36.9 143.4 4.1 196.7 36.9 1974 90.2 12.3 24.6 307.4 348.4 - 61.5 24.6 61.5 1975 65.6 8.2 4.1 4.1 - 24.6 28.7 8.2 1976 8.2 8.2 45.1 90.2 709 840.2 909.8 639.3 Goniobasis virginica 1972 57.4 110.7 213.1 61.5 1973 102.5 86.1 110.7 20.5 57.4 61.5 45.1 36.9 5254.1 2954.9 1524.6 2368.9 1974 1000 282.8 1209 561.5 639.3 1422.1 1717.2 5020.5 3434.4 5381.1 3073.8 3614.8 1976 557.4 3868.9 561.5 1643.4 1422.1 2123 1196.7 2647 . 5 1332 885.2 987.7 Goniobasis virgtntca 1972 12.3 8.2 4.1 1973 4.1 8.2 4.1 77.9 24.6 16.4 69.7 1974 94.3 28.7 49.2 36.9 45.1 77.9 430.3 655.7 2561.5 4131.1 3766.4 2028.7 1975 1561.5 2077.9 2692.6 2426.2 2729.5 3446.7 1692.6 1286.9 1401.6 713.1 3024.6 1976 2327.9 3282.8 5770.5 1024.6 987.7 885.2 166.2 2397.5 1963.1 3471.3 897.5 1967.2 Pisidum spp.
-- 7o 1972 61.5 4.1 12.3 32.8 36.9 1973 12.3 16.4 4.1 28.7 4.1 1974 8.2 8.2 32.8 49.2 49.2 98.4 61.5 86.1 1976 8.2 172.1 368.9 393.4 1069.4 1778.7 442.6 127 S76760 1972 8.1 5.4 24.6 4.1 1973 16.4 8.2 4.1 4.1 12.3 4.1 1974 8.2 45.1 4.1 41 950.8 143.4 270.5 139.3 172.1 282.8 86.1 77.9 1975 4.1 4.1 151.6 905.7 454.9 295.1 184.4 1976
0 LGS EROL Page 7 of 7 TABLE 2.2-16 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Spherium spp.
S75770 1972 - - - - 77.9 - 8.2 373 73.8 627 491.8 327.9 1973 77.9 28.7 86.1 20.5 32.8 45.1 - - 4.1 32.8 36.9 20.5 1974 12.3 - 8.2 4.1 4.1 237.7 176.2 590.2 422.1 897.5 868.9 405.7 1976 - 241.8 49.2 86.1 131.1 221.3 196.7 319.7 213.1 463.1 168 65.6 S76760 1972 - 2.7 2.7 - - 41 - 12.3 8.2 69.7 151.6 168 1973 41 45.1 4.1 - - 32.8 - - - - - -
1974 24.6 - - - 3W.8 114.8 311.5 245.9 - 127 -
1976 36.9 32.8 69.7 - 12.3 28.7 86.1 200.8 180.3 188.5 139.3 73.8 578620 1972 - - - - - - - - 57.4 610.7 4356.6 4016.4 1973 573.8 168 123 143.4 118.9 582 - 8.2 614.8 69.7 139.3 28.7 1974 24.6 24.6 - 16.4 - 73.8 - 463.1 709 1004.1 573.8 1000 1975 - 45.1 - 53.3 49.2 - - - 36.9 - 12.3 -
1976 36.9 32.8 69.7 - 12.3 28.7 86.1 200.8 180.3 188.5 139.3 73.8
0 LGS EROL Page 1 of 5 TABLE 2.2-17 MONTHLY DENSITIES(I) OF IMPORTANT SPECIES (TAXA) OF BENTHIC MACROINVERTEBRATES COLLECTED FROM THE SCHUYKILL RIVER, 1972 THROUGH 1974 Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec 1972 0.0074 0.5434 0.1123 1973 0.0004 0.0033 0.0012 0.0082 1974 0.0033 0.0045 0.0025 S76760 1972 0.0003 0.0011 0.0003 0.0053 0.2311 0.0295 0.0057 1973 0.0004 1974 0.0025 0.0012 0.0004 S78620 1972 0.0005 0.0091 0.0971 0.0881 0.0242 1973 0.004 0.0037 1974 - 0.0004 0.0074 0.0250 0.0332 0.0037 0.0061 0.0025 Prostoma graecense 575770 1972 0.1000 0.2045 0.0037 1973 0.0053 1974 0.0020 0.0086 0.0016 S76760 1972 0.0602 .0.0508 0.0098 1973 0.0143 0.0094 -
S78620 1972 0.0123 0.0234 0.0689 0.0029 1973 0.0004 1974 - 0.0025 0.0025 0.0012 0.0025 0.0090 Tubiftcidae S75770 1972 0.4648 - 4.2992 0.8041 1.0152 0.1451 0.1037 0.3127 1973 0.5242 0.0234 0.2857 0.2352 0.6152 2.4869 0.4828 0.1295 0.5967 0.0189 0.1529 0.0049 0.4242 0.1742 0.4414 1.5459 0.2053 0.0512 0.0422 0.1602 0.2721 0.0615 1974 0.1201 0.8443 S76760 1972 0.0051 0.0433 0.4475 1.5955 0.5316 0.4840 0.2549 0.4439 1.3529 0.0288 0.1462 0.6906 0.9602 1.3340 0.7016 0.1967 0.4971 0.7303 0.2324 0.0467 1973 1.0152 0.2139 0.2541 0.3049 1974 0.2619 2.8045 0.3684 0.7270 2.4213 1.7984 0.8422 0.2902 0.0607 S78620 0.1865 0.0840 0.1283 0.0955 1972 0.3078 0.0049 1973 0.1533 0.0332 0.1037 0.1459 0.4373 0.8861 0.4316 0.0209 0.0492 0.0516 0.3742 0.9975 0.0488 0.0057 0.0172 0.0324 0.0803 0.2430 1974 0.2086 0.9217 0.3676 0.1139
LGS EROL Page 2 of 5 TABLE 2.2-17 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Crangonx graoilts 575770 1972 - - - 0.0123 - 0.0033 1973 0.0008 - 0.0029 - 0.0160 0.0016 0.0012 0.0328 - - 0.0275 1974 0.0008 0.0143 0.0115 0.0029 0.0143 0.0074 0.0070 0.0082 0.0176 0.0061 0.0270 0.0012 S76760 1972 0.0061 0.0488 0.0029 1973 0.0053 0.0037 - - 0.0053 - 0.0066 0.0012 0.0574 0.0135 0.0828 1974 0.0012 0.0152 - 0.0148 0.0143 0.1758 0.0098 0.0148 0.0004 0.0225 S78620 1973 0.0029 - -o 0.0008 0.0016 0.0033 0.0139 0.1561 0.0221 0.0020 1974 0.0020 0.0176 - 0.0316 0.0287 0.1545 0.0025 0.0029 0.0041 0.0041 0.3107 0.0545 Cambarus bartoni S75776 1974 - 3.9622 - - - - - - -
S76760 1972 - 3.2631 1973 0.0689 S78620 1973 0.0143 Orconectes spp.
S75770 1973 . -- - 0.0361 - - 2.8734 1974 - 2.6914 - 8.3566 2.9266 13.8590 576760 1972 - - 1.5475 1973 - - -- - 0.0348 - 4.1734 1974 . - 0.0520 - 4.3705 - 4.0172 -
578620 1972 - 6.4008 -
1974 .- - - 0.0430 - 0.3902 - - 4.3988 1973 - - 0.1586 - 0.0283 0.0111 1974 0.0197 0.0082 0.0131 0.0061 0.0004 0.0246 - 0.0164 0.1770 0.1594 0.3898 0.0758 S76760 1972 0.0033 1973 0.0176 0.0299 0.1766 0.0574 1974 0.0238 0.0070 0.0090 0.0189 0.0168 0.0262 0.0635 0.0279 -
578620 1972 0.0086 1973 - 0.0447 - - 0.1520 0.0414 0.0709 0.0086 1974 0.0037 0.0135 0.0250 0.0197 0.0221 0.1037 0.0193 0.0164 0.1832 0.1291 0.0414 0.0258
LGS EROL Page 3 of 5 TABLE 2.2-17 (Cont' d)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Cheumatopsyche S75770 1972 - - 0.0020 -
1973 0.0004 - 0.0012 0.0061 - - - 0.0012 - 0.0127 1974 0.0049 0.0086 0.0004 - 0.0057 0.0029 0.0020 0.0193 0.0975 0.0525 576760 1972 0.0148 0.0027 0.0102 - 0.0098 = 0.0053 - -
1973 0.0004 0.0004 0.0041 - 0.0025 0.0041 0.0242 0.0066 1974 0.0434 0.0148 0.0225 0.0020 0.0029 0.0107 - 0.1541 -
S76720 1972 0.1083 0.1621 - - 0.0078 - - 0.0037 - - 0.0053 1973 0.0004 0.0127 0.0131 0.0033 - 0.0086 - 0.0070 0.1996 0.7061 0.5377 0.3811 1974 0.0930 0.1176 0.0078 0.1467 0.1045 0.0885 0.5180 3.5971 0.6197 1.6074 0.3676 0.3939 Hydropyche phalerata S75770 1974 - 0.0193 0.0008 0.0029 0.0016 S76760 1972 - 0.0048 1974 0.0131 S78620 1972 - 0.0228 - - - 0.0053 1974 0.0004 - - 0.0516 0.0225 0.0111 0.0143 0.0205 Chironomidae (larvae)
S75770 1972 S - 0.3443 - 0.0037 0.1184 0.2066 0.0377 0.0119 -
1973 0.0086 - 0.0275 0.0291 0.0730 0.2270 0.0398 0.1184 1.1086 - 0.0180 0.0082 1974 0.0807 0.0943 0.1348 0.0746 0.0602 0.1705 0.0078 0.0102 0.0008 0.0037 0.0332 0.0803 S76760 1972 0.0210 0.0175 0.0890 0.1806 - 0.5889 0.0033 0.1459 0.2016 0.1070 0.0311 0.0111 1973 0.0143 0.0205 0.0336 0.0930 0.0426 0.1611 0.0959 0.0955 0.5205 0.0070 0.0107 0.0377 1974 0.0811 0.0193 0.1484 0.0832 0.0943 0.1225 0.0221 0.0217 0.0016 - 0.0143 -
S78620 1972 0.0059 0.0331 - - 0.0073 0.0639 - 0.1074 0.1189 0.0824 0.0516 1973 0.0488 0.0414 0.0947 0.7680 0.6725 0.1434 0.1885 0.0734 0.9381 0.0857 0.0639 0.0807 1974 0.0639 0.2135 0.9049 0.4180 0.3512 0.5250 0.1799 0.0025 0.0057 0.1475 0.0766 0.3926 Chironomidae (pupae)
S75770 1972 0.0102 - - 0.0139 0.0041 0.0008 0.0012 1973 0.0057 0.0201 0.0004 0.0008 0.0303 - -
0.0016 0.0004 0.0020 0.0025 - -- - 0.0016 1974 S76760 1972 0.0011 0.0027 0.0097 0.0559 - 0.0045 - 0.0119 0.0197 0.0037
- - 0.0082 0.0033 0.0078 0.0004 0.0008 0.0061 -
1973 1974 - - 0.0049 0.0061 0.0045 0.0004 - -
S78620 1972 0.0022 0.0027 - - 0.0148 0.0066 - - 0.0074 0.0205 - -
- - 0.0008 0.0246 0.0283 0.0074 - 0.0004 0.0639 0.0066 - -
1973 1974 - 0.0045 0.0115 0.0156 0.0172 0.0172 0.0025 - - 0.0107 0.0033 0.0008
LGS EROL Page 4 of 5 TABLE 2.2-17 (Cont'd)
Taxon Station Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec 37577U 1972 0.0008 0.0086 0.0611 0.1537 1.9168 1.3844 2.2500 1973 0.4586 0.2184 0.1992 0.1746 0.0033 0.1500 0.0307 0.1828 0.0594 0.0721 2.0434 1974 1.3770 0.2492 1.5791 0.0770 0.0057 0.2357 0.0361 0.4176 0.1041 0.0750 0.7553 0.1459 S76760 1972 - 0.0142 - 0.0225 - 0.0275 0.1266 0.6484 1.1738 0.4869 1973 0.3426 0.0975 0.0037 0.0865 - 0.0053 0.0008 0.1930 0.4217 1.4996 1974 0.5471 0.2779 0.0447 0.0520 0.0197 0.5332 0.1537 0.9553 - 0.5475 S78620 1972 - 0.0030 - - - 0.0471 - - 2.1189 6.3684 24.3574 11.0578 1973 2.0766 1.3430 0.5107 0.2971 0.2148 0.2832 0.0168 0.0098 3.2594 2.1102 5.6340 8.5111 1974 0.8885 1.0803 0.3791 0.4984 0.0443 1.7197 3.0475 1.5742 0.1361 0.1906 0.2857 0.4734 Helisomna anceps 1972 - - - - 0.3291 - - 0.0045 0.3176 1.8049 1.6557 1.2402 1973 0.1418 0.0045 0.1586 0.1619 - 0.0566 - 0.0209 0.1574 0.0307 0.0324 1974 0.0369 0.0172 0.0709 0.0742 - - 0.4193 0.5689 0.0963 0.0119 0.2041 0.0820 S75760 1972 0.0177 0.0422 0.0881 0.0078 0.0348 0.0709 0.1920 1973 0.1787 0.0102 - 0.0008 0.0984 0.2488 1974 0.0459 0.2389 0.0094 0.1033 0.1496 0.3037 0.1463 S78620 1972 1.5639 5.4352 8.1299 1973 3.6049 2.6869 3.1061 2.3832 0.4049 0.0324 1.0467 0.6246 0.6742 3.7697 1974 1.0508 0.7123 0.3291 0.1344 0.0172 0.3111 14.9455 6.3004 1.9910 0.9836 0.5316 4.4525 Ferrissia tarda
$75770 1972 - - - 0.0102 0.0016 0.0434 0.0098 0.0582 0.1258 0.0713 1973 0.0225 0.0102 0.0061 0,0287 0.0053 0.0148 0.0012 0.0078 0.0361 1974 0.0127 - - 0.0029 - 0.0615 0.0086 0.0029 S75760 1972 - - - 0.0025 0.0373 0.2832 0.2033 0.1180 1973 0.0156 0.0041 0.0201 0.0139 - 0.0070 0.0025 - 0.0160 1974 0.0221 - 0.0016 0.0094 0.0049 0.0520 0.0275 -
S78620 1972 0.0005 0.0035 -- - 0.0844 0.0955 0.4947 0.1123 1973 0.0561 0.0098 0.0156 0.0283 0.0373
-6 0.0119 0.0008 - 0.0336 0.0053 1974 0.0393 - 0.0066 - 0.0061 0.0783 0.0344 - 0.0201 0.0012 0.0143 Gonlobasis v irgtnca 775=1 0.2574 1972 0.0881 0.5738 1.1766 0.4955 1.3615 0.2234 0.5340 0.5254 0.4836 1.5074 47.6455 24.0398 17.3852 19.1386 1973 0.5570 3.3512 10.8115 5.7316 9.5020 21.1988 26.0893 36.4881 36.6448 58.0352 44.5340 42.5615 1974 9.0738 5.0680 41.1033 6.1971 16.2102 21.1742 32.0352 17.3602 44.9004 15.5820 18.0131 17.8975 1976
0 LGS EROL Page 5 of 5 TABLE 2.2-17 (Cont' d)
Taxon Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Gonlobasis virginica (Cont'd 575760 1972 - 0.0115 0.0648 0.0750 0.0418 1973 - - 0.0172 - 0.0332 - 0.1566 0.9820 12.2066 34.5393 17.1025 1974 3.6234 5.5857 5.8020 5.6201 4.0266 10.2061 15.6742 35.4242 50.9283 - 185.0918 -
1975 - 39.0115 65.7135 21.5807 18.3602 17.8172 15.3480 85.2529 67.5340 14.7730 10.8668 10.3922 1976 19.3492 18.7230 21.5213 2.4172 6.4840 57.4967 33.4713 19.6307 62.1303 15.3217 9.5873 3.3094 S78620 1972 - - 0.0102 0.0193 0.0057 -
1973 - 0.0045 - - 0.0111 0.0205 - 0.2738 0.1295 0.0725 0.3926 1974 1.2299 0.1988 0.3377 0.3598 0.3730 0.8836 12.0623 7.0311 22.5266 37.7291 17.5402 14.8689 1975 - 13.5430 15.9520 25.8467 14.0238 13.9697 20.0869 9.2959 8.2000 8.7307 6.7922 22.6270 1976 12.9582 24.4447 44.5098 8.0561 10.9562 10.8734 4.6262 7.3779 13.8287 31.4520 7.9697 34.7541 Pisidum spp.
1972 - - - 0.0086 - 0.0004 0.0045 - 0.0070 0.0234 -
1973 0.0033 0.0098 0.0020 0.0057 - - - 0.0004 -
1974 - - 0.0016 0.0020 0.0209 - 0.0057 0.0094 0.0127 0.0061 0.0205 S75760 1972 0.0022 0.0008 0.0258 0.0012 1973 0.0086 0.0004 0.0008 0.0012 - - 0.0012 0.0279 1974 0.0004 0.0045 0.0025 0.0082 -
S78620 1972 0.0434 0.0463 1973 0.1131 0.0193 0.0193 0.0291 0.0180 0.0385 0.0008 -
1974 - - - 0.0066 0.0012 - 0.0029 0.0061 0.0123 0.0090 0.0209 Sspp.
1972 - 0.0193 - 0.0082 0.0553 0.0344 0.1988 0.1344 0.0828 0.0131 0.0053 0.0205 0.0340 - - 0.0012 0.0393 0.0881 0.0959 1973 0.0070 0.0025 1974 0.0406 - 0.0189 0.0074 0.0230 0.1004 0.0861 0.3197 0.3693 0.2156 0.2594 0.1131 S75760 0.1164 0.0586 1972 0.0005 0.0003 0.0287 - 0.0148 0.0025 0.0098 1973 0.1176 0.0266 0.0041 0.0332 0.0143 0.0094 0.2270 0.1787 - 0.0291 -
1974 S78620 2.0410 2.4287 1972 - - 0.0115 0.0406 0.1012 0.0258 0.0316 0.2123 - 0.0020 0.7598 0.0697 0.3111 0.0717 1973 0.6492 0.0828 0.2828 0.4074 1974 0.0770 0.0434 - 0.0037 - 0.1184 - 0.3123 0.5902 0.3541 M1 )iouiass, grams per meter
IGS EROL TABLE 2.2-18 TCTAL NUMBEP OF SPECIES (TAXA) OF BENTHIC MACPCINVERIEERATES COLLECTED PER SAMPLE FROM THE SCHUYIKILL RIVER NEAR LIMERICK GENERATING STAIICN, 1973 tbrouqh 1976 Mean No.
Station/Year Jan Feb Mar Arr May Jun Jul Aug Sep Oct Nov Dec Taxa/Year S78620 1973 26 19 16 23 15 30 15 14 20 20 20 17 19.6 1974 17 34 14 28 31 28 27 25 14 24 18 26 23.8 1975 - 27 14 18 27 24 22 28 28 22 21 15 22.4 1976 24 17 17 23 23 30 33 27 31 31 27 29 26.0 S76760 1973 24 16 14 16 7 15 12 10 14 22 22 19 15.9 1974 28 17 20 21 16 18 20 19 15 - 23 - 19.7 1975 - 33 27 22 28 18 14 22 27 27 20 23 23.7 1976 26 17 13 15 16 19 22 20 28 27 24 27 21.2 s75770 1973 17 13 18 16 18 18 9 12 17 8 16 12 14.5 1974 27 22 18 24 11 19 15 19 15 25 20 25 20.0 1976 - 25 20 20 18 23 20 22 24 22 20 19 21.2
0 LGS EROL Page 1 of 2 TABLE 2.2-19 MONTHLY PERCENT COMPOSITION OF DOMINANT DRIFT SPECIES (TAXA)
OF MICROINVERTEBRATES COLLECTED FROM THE SCHUYKILL RIVER AT 577560, 1972 THROUGH 1975 Taxon Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Naididate 1972 (1) 1.8 1974 1.4 1975 2.9 Tricorythodes (nymphs) 1972 (1) (1)
(1) (1) (1) 1973 2.2 1.9 (1) 1.4 1974 (1) (1) 6.6 17.8 (1) 1975 8.7 2.4 (1) 41.5 5.2 Cheumatopsyche (larvae) 197Z 1.8 (1) (1) (1) (1) (1) 1973 (1) (1) (1) (1) (1) 1.1 (1) (1) (1) 2.7 2.3 1974 1.9 7.6 (1) (1) (1) (1) 4.5 6.3 5.2 10.0 (1) 1975 (1) 5.3 1.5 2.7 2.9 30.4 Hydropsyche phalerata (larvae) 1972 1.8 (1)
(1) 1973 (1) (1) (1) - (1) (1) (1) (1)- (1) 1974 - - (1) - 15.1 1975 - 1.4 7.8 1.4 15.2 30.4 Hydroptila spatula (larvae) 1972- (1) (1) 1973 (1) 1974 1975 (1) 2.7 1.2 (1) 15.2 Pcde (larvae) 2.7 (1) 2.3 19.6 1973 2.6 1.7 49.6 4.8 (1) (1) (1) (1) 1974 10 3.5 5.7 (1) (1)
(1) (1) 1975 P de (pupae) 23.4 - 22.8 2.8 (1) 2.4 26.8 22.9 1973 55.2 59.1 29.5 9.9 (1) (1) (1) 1.9 1974 33.1 30.6 70.2 24.9 (1) (1) (1) 1.9 1975 (1) (1) (1)
0 LGS EROL Page 2 of 2 TABLE 2.2-19 (Cont'd)
Taxon Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Telematoscopus albipunctatus (lIarvae) 1972 (1) 3.1 4 1973 1.4 (1) (1) (1) (1) (1) (1) 3.6 1974 27 5.3 2.3 (1) 3.4 Telmatoscopus albipunctatus (pupae) 1972 (1) 1.2 58.5 48.2 1973 30.4 7.1 1.2 - (1) - 39.3 1974 6.5 20.6 1.2 2.3 -(1) (1) - (1)
Chironomidae (larvae) 1972 - 16.2 - 23.5 19.7 40 52.2 58.8 26.4 7.6 3.7 1.4 1973 (1) 18.2 10.9 55.4 - 42.3 55 60.9 67.8 43.7 45.9 43.9 1974 14 21.8 8.3 34 59.7 68.9 77.4 51.1 41.1 24.7 50 13.2 1975 - - 81.5 48.7 72.5 65.6 2078 23.7 Chironomidae (pupae) 1972 - 34.2 - 47.9 75.6 46.2 36 39.9 68.6 75.3 (1) (1) 1973 8.3 8 7.5 26.7 - 33 37.4 37.2 30.3 38.7 41.1 6.3 1974 1.7 3.5 13.1 32.4 35.8 30.3 19.8 23.7 24.8 19.2 10 79.8 1975 - - 14.5 16.9 9.9 27.2 12.3 6.7
( 1 )Less than 1%.
LGS EROL Page 1 of 2 TABLE 2.2-20 MONTHLY DENSITIES(I) OF SELECTED SPECIES (TAXA) OF MICROINVERTEBRATES COLLECTED IN DRIFT SAMPLES FROM S77560 IN THE SCHUYLKILL RIVER, 1972 THROUGH 1975 Annual Mean Taxon/Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Now Dec Density Nat di dae 1972 0 0 0 0 3.3 11.6 0 11.6 6.6 0 3.3 1973 0 0 0 14356.1 0 8.8 0 0 0 0 1436.5 1974 0 0 0 1060 8 0 0 0 0 0 0 0 88.4 1975 284.7 0 0 0 0 0 47.5 Trtcorythoses 0 0 1972 0 0 0 3.3 0 5.8 3.3 0 1.1 0 1.4 1973 0 00 0 1978.1 8.1 66.3 8.9 7.7 0 195.4 1974 0.8 0 0 10.5 46.3 54.7 00 2.7 9.6 1975 0 106.3 38.6 24.6 1423.3 3.1 266 Cheumatopsyche spp. 5.1 197Z 2.7 3.6 0 6.6 11.6 0 0 8.8 4.5 4.3 1973 1.8 3.4 3.9 2.2 349.3 32.9 8 17.8 0 20.7 6.6 40.6 1974 37 18.2 13.4 10.5 5.7 0 31.8 122.1 79.6 8.4 2.9 21.8 29.3 1975 6.9 65.2 23.9 86.8 98.7 8.2 47.5 Hydropsyche phalerata M92 1973 1974 0 0 0 0 0 0 5.8 0 0 0 0 0 0.5 1975 17.1 123. 3.6 177.6 19.1 56.8 Hydroptila spatula 1972 1973 0 1974 0 0 0 0 0 0 0 0 0 0 0.4 1975 3.5 33.4 19.3 0 521.3 0 96.3 fcda (larvae) 4.1 2.6 0 0 0 0 0 0 59.5 473.6 54 1973 18.9 5.1 2283.4 61.2 42.1 3 0 12.5 0 0 5.8 221.1 0 0 21.8 30.7 1974 92.1 8.4 127.6 16.1 2.4 0 0 0 0 1975 1.7 0 0 0 0 0.4 0.4 f!cda (pupae) 35.4 625 391.7 0 0 0 3.3 15.4 564.4 506.6 214.2 1973 4A9.7 178.3 1204.3 126.9 84.2 3.7 6.4 0 0 0 24 190.7 1974 6:35.8 73 1576.1 378.8 354.9 2.7 0 0 9.3 0 0 43 256.2 1975 27.8 0 0 0.7 0 0 4.8 Telmatscopus albipunctatus (la-rvae) 1972 0 0 0 0 0 0 0 0 65 94.4 15.9 1973 10.4 0.9 5.5 0.7 4.2 3.7 9.6 3.6 0 0 40.5 7.2 1974 0 0 0 0 0 0 0 0 0 0 0 133.4 11.1 1975 0 0 0 0 0 0 0
LGS EROL Page 2 of 2 TABLE 2.2-20 (Cont'd)
Annual Mean Taxon/Year Jan Feb Mar Apr May Jun Jul Aug Sep Oct Now Dec Density Telmatoscopus albipunctatus (pupae) 1972 - 0 - 28.3 0 0 0 0 0 7.7 1264.3 1069.3 237 1973 1.8 21.4 39.7 0 = 0 0 5.6 0 0 0 490.7 50.8 1974 0 0 0 0 0 0 0 0 0 0 0 0 1975 .... 0 0 0 0 0 0 - . 0 Chironomtdae (larvae) 1972 24.5 - 794.8 2777.8 2570.8 585.3 7465.3 750.7 46.3 86 30.3 1413.2 1973 4.9 53.2 345.6 703.4 - 34528.6 2518.7 18054.8 11100.4 240.7 419.1 548.1 6228.9 1974 268.5 51.9 185.2 956.8 44400.6 13883.4 15593.2 1378.4 518.5 75.8 24.5 520.2 6487.3 1975 .... 8125 593.3 1143.5 2073.2 711.4 15 - 2110.2 Chironomidae (pupae) 1972 51.7 - 2062.8 10644.6 2109.8 403.4 5063.7 1951.1 563.3 16.3 4.5 2284.4 1973 0 24.0 237.5 339 - 26906.6 17777.9 11964.4 4568.9 213 375.2 79 4226 1974 33.2 8.4 293.2 857.2 27383 6108.4 5269.1 639.7 313 58.9 2.9 3137.3 3675.4 1975 .... 1442.7 205.8 155.9 860.8 421.5 4.1 - 515.1
( 1 )Number of organisms/lOOM3 .
LGS EROL TABLE 2.2-21 MONTHLY ESTIMATES(') OF THE PERCENT OF BENTHOS DRIFTING IN THE SCHUYLKILL RIVER NEAR LIMERICK GENERATING STATION, 1972-1975 1972 1973 1974 1975 Jan (2) 0.0088 0.0741 (2)
Feb 0.0094 0.0058 0.0024 (2)
Mar (3) 0.0504 0.0068 (2)
Apr (3) 0.0059 0.0227 (2)
May 1.3140 (2) 0.5727 0.0675 Jun 0.0651 0.3611 0.1035 0.0050 Jul (3) 0.0377 0.1669 0.0067 Aug (3) 1.2039 0.0121 0.0155 Sep 0.0016 0.0559 0.0119 0.0185 Oct 0.0014 0.0103 0.0019 0.0010 Nov 0.0036 0.0149 0.0002 (2)
Dec 0.0065 0.0182 0.0159 (2)
(1) Estimates are based upon benthos densities at S78620 and drift densities at S77560.
(2) No drift samples taken.
(3) No benthos samples taken.
LGS EPOCL TABLE 2.2-22 (Page 1 of 2)
FISHES AND HYBRIDS(1) CCLLECTED IN THE VICINITY OF LIMERICK GENERATING STATION, SCHUYLKILL RIVER, 1970-1976 Scientifi, EAM Relative Mfundancg BoIin famil~ Amiidae Bowf in MAia calya (Linnaeus) Rare Ix Freshater eel .~jfmli Anqui.llidae American eel AoaIuilli rosrat (Lesueur) Common Salmonidae Rainbow trout Sal aairdneri (Richardson) Rare I Brook trout Rare3 N Salvel.nu fontinal (Mitchill)
PIkfImilx Esocidae Redfin pickerel Eso americanus americanus (Gmelin) Rare Muskellunqe Rare I Zo maeguinon (Mitchill)
Minno. fami Cyprinidae Gold fish CaUassLu auratus (Linnaeus) Common I Carp Common I Cvrinu8 cario (Linnaeus) I Goldfish x carp hybrid S. auzaiu x _C. carrio hybrid Uncommon Uncommon N Cutlips minnow ExoZloseu maxillinaua (Lesueur) N Golden shiner jQ+/-.gum crvsoleucas (Mitchill) Common Common N Comely shiner Mg.troiL amoenus .f(Abbott) N Common shiner Notrovis cornutue (Mitchill) Common Common N Spottail shiner Notois hudsonflu (Clinton) N Abundant Notropies zrogne Notxoro (Cope)(Cope)
Swallowtail shiner N Spotfin shiner ioyer Abundant Pimebales noatus (Rafinesque) Uncommon N Bluntnose minnow I Fathead minnow PimeDhales Dromelas Pafinesque Rare Common N Blacknose dace B hys atratulus (Hermann) N Lonqnose dace Rbinicbtbvs cataractae (Valenciennes) Uncommon Uncommon N Creek chub Seoim atromaculatus (Mitchill) N Fallfish Semotilus corporalis (Mitchill) Uncommon
IABLE 2.2-22 (Cont'd) (Page 2 of 2 )
Relative Status Abundance Sucker family Catostomidae Quillback Cazriodes cprinu (Lesueur) Rare N White sucker Catostopus commersoni (Lacepede) Abundant 14 Creek chubsucker jjmz oblong (Mitchill) Common 14 fteshwate~ catfish failJ1 Ictaluridae White catfish Ictalurus catus (Linnaeus) Common N Yellow bullhead Ictaluru natali (Lesueur) Common V Brown bullhead Ictalurus nebulgus (Lesueur) Abundant N Channel catfish Ictalurus Dunctatus (Rafinesque) Uncommon I Marqined madtom Noturu snsig (Richardson) Rare N Cyprinodontidae Banded killifisb Fundula diaphanus (Lesueur) Common Sunfis famil Centrarchidae Rock bass Ambnin rupestri (Rafinesque) Common I Redbreast sunfish Lenma auritus (Linnaeus) Abundant Green sunfish Common N Levomi cvanellus (Rafinesque) I Pumpkinseed lm (bbos (Linnaeus) Abundant N Blueqill 1eo 3 macrochirus (Rafinessque) Common I Sunfish hybrid lepomi hybrid Common Smallmouth bass Micronterus do oieu (Lacepede) Uncommon I Larqemouth bass Microuterus salmoides (Lacepede) Common I White crappie Pomgg annulari (Pafinesque) Common I Black crappie Pmoxia nicromaculatus (Lesueur) Common I ferxc fmi1l Percidae Tessellated darter Etbeostoma lmstedi (Storer) Common N Yellow perch Perca flavescens (Mitchill) Uncommon Walleye Stizostedion vitreu vitreum (Mitchill) Rare I I Reference 2.2-53 2 1 = introduced, N = native 3 Only collected in a tributary of the river.
0 LGS EROL TABLE 2.2-23 MEAN DENSITY AND RELATIVE ABUNDANCE OF SELECTED LARVAL FISH COLLECTED FROM THE EAST CHANNEL OF THE SCHUYLKILL RIVER AT s77560, MAY-AUGUST IN 1974, 1975 and 1976 1974 1975 1976 Taxa No./m 3 ____ No./m 3
_ No./m 3 Minnows 0.21337 47.1 0.06908 78.1 0.14634 24.6 Goldfish 0.13611 30.0 0.00020 0.2 0.37527 63.0 Carp 0.04465 9.8 0.00102 1.2 0.04117 6.9 Golden Shiner 0.02186 4.8 0.00020 0.2 0.00670 1.1 White Sucker 0.00109 0.2 0.01328 15.0 0.00422 0.7 Brown Bullhead 0.00016 - 0.00082 0.9 0.00025 0.0 Banded Killifish 0.00109 0.2 0.00123 1.4 0.00050 0.1 Lepomis Sunfish 0.03503 7.7 0.00123 1.4 0.01959 3.3 Tessellated Darter - - 0.00143 1.6 0.00174 0.3 0.45374 0.08850 0.59578
LGS EROL TABLE 2.2-24 HORIZONTAL VARIATION IN DENSITY OF LARVAL FISH COLLECTED FROM THE SCHUYLKILL RIVER AT S77560 in 1975 NET 1975 1 2 3 4 5 6 3 3 3 3 3 3 Taxa No./m No./m No./m No./m No./m No./m Minnows 0.2493 0.0254 0.0237 0.0238 0.0341 0.0834 Goldfish 0.0071 - 0.0003 0.0004 - 0.0007 Carp 0.0013 - 0.0003 0.0014 0.0022 0.0033 Golden Shiner 0.0033 0.0010 0.0007 0.0009 0.0004 0.0009 White Sucker 0.1790 0.0157 0.0096 0.0181 0.0160 0.0420 Brown Bullhead 0.0004 0.0003 0.0010 0.0014 0.0004 0.0005 Banded Killfish 0.0009 0.0005 0.0007 0.0003 0.0006 0.0013 Lepomis Sunfish 0.0083 0.0010 0.0011 0.0009 0.0009 0.0021 White Crappie 0.0536 0.0046 0.0082 0.0151 0.0060 0.0126 Tessellated Darter 0.0020 - 0.0006 0.0016 0.0017 0.0029 1976 Minnows 0.1796 0.0586 0.0925 0.0628 0.1719 0.1910 Goldfish 0.0489 0.0552 0.0442 0.0350 0.1631 0.0858 Carp 0.0322 0.0272 0.0203 0.0202 0.1053 0.1017 Golden Shiner 0.0100 0.0037 0.0018 0.0013 0.0199 0.0247 White Sucker 0.0059 0.0017 0.0019 0.0034 0.0062 0.0118 Brown Bullhead 0.0000 0.0000 0.0000 0.0000 0.0026 0.0000 Banded Killfish 0.0011 0.0002 0.0002 0.0007 0.0000 0.0005 Lepomis Sunfish 0.0323 0.0085 0.0076 0.0069 0.0334 0.0490 White Crappie 0.0000 0.0000 0.0007 0.0013 0.0048 0.0041 Tessellated Darter 0.0014 0.0011 0.0007 0.0036 0.0067 0.0015
LGS EROL TABLE 2.2-25 TOTAL CATCH AND RELATIVE ABUNDANCE OF LARVAL FISH COLLECTED BY TRAP NET FROM THE SCHUYLKILL RIVER SHORELINE AT S77560, MAY-AUGUST IN 1975 Total %
Taxa Catch Catch Minnows 621 46.4 Goldfish 495 37.3 Carp 98 7.3 Golden shiner 26 1.9 White sucker 61 4.6 Brown bullhead 4 0.3 Banded killifish 3 0.2 Lepomis sunfish 15 1.1 White crappie 5 0.4 Tessellated darter 11 0.8 TOTAL 1339 100.0 TOTAL 1339 100.0
LGSEEO TABLE 2.2-26 TOTAL NUMBER AND PERCENT CATCH OF SHORELINE LARVAL FISH SAMPLED BY PUSH NET FROM THE SCHUYLKILL FIVER DURING THE SPA*INING PERICD IN 1976 Stations' S78973 S78432 S77970 S77550 S77485 S77320I S77230 Total Total Total % Total % Total % Total I Total Taxa No. Catch N2. Catch No. Catch :Ij _No. gatcb Unidentified minnows 68 54.0 20 83.3 53 46.9 1 25.0 0 0.0 6 3.6 0 0.0 Carp 0 0.0 0 0.0 12 10.6 0 0.0 0 0.0 15 8.9 0 0.0 Gold fish 0 0.0 0 0.0 27 23.9 2 50.0 0 0.0 135 80.4 0 0.0 Golden shiner 1 0.8 0 0.0 4 3.5 0 0.0 0 0.0 0 0.0 0 0.0 White sucker 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 Lepomi spp. 57 45.2 4 16.7 10 8.8 0 0.0 1 100.0 4 2.4 5 100.0 Banded killifish 0 0.0 0 0.0 7 6.2 1 25.0 0 0.0 8 4.7 0 0.0 Tessellated darter 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 Total 126 24 .113 4 1 168 5 Stations' S77161 S76970 S76840 S7 6794 S76632 S75781 Comtined Total Total % Total Total Total Total Total Taxa No. Catch No. catc NO, catch NO Catc H. Clich 5o. catc _No. Catc Unidentified minnows 131 50.2 27 15.1 1 10.0 1 0.4 34 50.0 3 13.6 345 2e.0 Carp 8 3.1 5 2.8 0 0.0 0 0.0 0 0.0 2 9.1 42 3.4 Goldfish 9 3.4 144 80.4 3 30.0 243 96.8 2 2.9 15 68.2 580 47.1 Golden shiner 21 8.1 1 0.6 1 10.0 1 0.4 0 0.0 0 0.0 29 2.4 White sucker 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 1 4.5 1 0.1 ILe.mi spp. 92 35.2 2 1.1 5 50.0 6 2.4 31 45.6 0 0.0 217 17.6 Banded killifish 0 0.0 0 0.0 0 0.0 0 0.0 0 0.0 1 4.5 17 1.4 Tessellated darter 0 0.0 0 0.0 0 0.0 0 0.0 1 1.5 0 0.0 1 0.1 Total 261 179 10 251 68 22 1232
'Stations S77970, S77161, and S76794 were located off the Chester County shore; all other stations were off the Montqomery County shore.
LGS EPOL TABLE 2.2-27 TOTAL NUMBER AND CATCH-PER-UNIT- EFFCRT OF LARVAL FISH COLLECTED BY PUSH NET FROM SELECTED AREASC() IN THE SCHUYLKILL RIVER NEAR LIMERICK GENERATING STATICI INi 1976 Upstream discharge Downstream discharge East Shore West Shore Total Total Total Total Taxa No. C/f NV, C/f I I III No. C/f No. C/i:
Unidentified minnows 148 24.67 197 28.14 160 16.00 185 61.67 Carp 27 4.50 15 2.14 22 2.20 20 6.67 Goldfish 164 27.33 416 59.43 301 30.10 279 93.00 Golden shiner 5 0.83 24 3.43 3 0.30 26 8.67 White sucker 0 0.00 1 0.14 1 0.10 0 0.00 LepomIs app. 76 12.67 1541 20.14 109 10.90 108 36.00 Banded killifisb 16 2.67 1 0.154 10 1.00 7 2.33 Tessellated darter 0 0.00 1 0.14 1 0.10 0 0.00 Total 5436 72.67 796 113.70 607 60.70 625 208.34
(')Each area represents a combinaticn of data from several sites within the area.
LGS EPOL TABLE 2.2-28 TOTAL CATCH, REIATIVE ABUNDANCE, AND FBEQUENCY OF OCCURRENCE (FO %) OF FISHES COLLECTED BY SEINE FPCH THE SCHUYLKILL RIVER (ALL SITES COMBINED) IN 1975 AND 1976 1975 1976 American eel 1 CI) 0.76 - - - 1 I)
Banded killifish 108 0.5 31.82 231 1.3 44.44 339 0.8 Black crappie 24 0.1 12.88 31 0.2 11.11 55 0.1 Blacknose dace 7 C') 5.30 109 0.6 24.31 116 0.3 Bluegill 43 0.2 17.42 63 0.4 24.31 106 0.3 Bluntnose minnow 3 (1) 1.52 13 0.1 8.33 16 (1)
Brown bullhead 17 0.1 7.58 20 0.1 8.33 37 0.1 Comely shiner 128 0.5 28.03 129 0.7 31.25 257 0.6 Common shiner 29 0.1 15.91 135 0.8 16.67 164 0.41 Creek chub - - - 9 0.1 5.56 9 (1)
Creek chubsucker 1 (1) 0.76 6 (1) 3.47 7 (a)
Cutlips minnow - - - 5 (1) 3.47 5 (2)
Fallfish 2 C*) 1.52 - - - 2 (")
Golden shiner 368 1.5 29.55 376 2.2 27.08 744 1.8 Goldfish 1 (1) 0.76 15 0.1 2.78 15 (1)
Green sunfish 61 0.3 26.52 71 0.4 25 132 0.3 Largemouth bass 10 (I) 5.30 12 0.1 4.86 22 0.1 Lepomis hybrid 7 (') 5.30 8 (I) 2.78 15 CI)
Lonqnose dace - - - 8 C() 4.17 A8 ()
Marqined madtor - 1 I- Cl) 0.69 1 (1)
Muskellunqe - - - 1 C() 0.69 1 (I)
Pumpkinseed 97 0.51 29.55 131 0.8 31.94 228 0.6 Quillback - - - 5 CI) 1.39 5 cI')
Redbreast sunfish 203 0.8 39.39 706 5.1 51.39 909 2.2 Rock bass 8 (1) 5.30 26 0.2 9.72 34 0.1 Smallmouth bass 1 (*) 0.76 6 (*) 2.78 7 (2)
Spotfin shiner 9259 38.7 87.88 8000 56.4 82.64 17259 41.9 Spottail shiner 44 0.2 14,.39 775 4.5 31.94 819 2 Swallowtail shiner 13426 56.1 78.03 5611 32.5 77.08 19037 46.2 Tessellated darter 32 0.1 14.39 257. 1.5 53.75 289 0.7 White catfish - - - 2 CI) 0.69 2 (1) white crappie 11 (I) 5.30 29 0.2 11.81 510 0.1 White sucker 19 0.1 6.82 449 2.6 23.61 468 1.1 Yellow bullhead 4 (2I) 3.03 8 (I) 3.47 12 CI)
Yellow perch - - - 1 cz) 0.69 1 C')
Total 23914 17248 41162 Tess than 0.1%
LI)
LGSEROL TABLE2.2-29 MONTHLY VARIATION IN TOTALCATCHANDRELATIVEABUNDANCE OF IMPORTANT SPECIES OF FISH ANDTOTALNUMBER OF SPECIES COLLECTED BY SEINEFROMTHE SCHUYLKILL RIVER (ALL SITES COMBINED, 1975 AND 1976)
Jan Feb par Apr may Jun Jul Aug Sep Oct Nov Dec S % % % % 1 % % % %
5 5%
Total Total Total Total Total Total Total Total Total Total Total Total Total Species(1) Year No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch American eel 1975 - 1 0.3 - 1 (2)
Muskellunge 1976 1 0.2 ... ..- 1 (2)
Goldfish 1975 - - - 1 0.S 1 (2) 1976 - 0'6 -9 0-.6 -- -
Swallowtail shiner 1975 3006 65.2 5902 77.7 1504 58.8 2431 45.5 185 10.6 77 14.0 11 2.1 40 38.1 82 20.7 32 19.0 108 56.5 48 63.3 13426 56.1 1976 301 66.4 77 69.2 71 48.0 53 16.3 2 0.6 24 2.2 316 22.2 271 9.7 219 10.6 - - 2008 50.2 2269 S0.8 5611 32.5 Spotfin shiner 1975 1339 29.1 1413 18.6 978 38.2 28S7 53.4 1545 87.4 423 76.9 448 83.9 20 19 120 30.2 71 42.3 33 17.3 12 13.3 9259 38.7 1976 67 14.8 29 22.3 56 37.8 210 64.4 184 57 35 3.2 169 11.9 1982 70.6 1616 77.9 - 1653 41.4 1999 44.7 8000 46.4 Whitesucker 1975 1 (2) 1 (2) - - - -2 0.1 12 12 3 0.8 - 19 0.1 1976 - -1 0.3 43 13.3 326 29.8 71 5.0 4 0.1 - 4 0.1 449 2.6 Grow bullhead 1975 - - - 4 0.7 9 2.3 3 1.8 1 0.5 17 0.1 1976 1 0.2 - "1 0.3 2 0.6 2 0.2 12 0.8 2 0.1 - 20 0.1 Banded killfish 1975 35 0.8 23 0.3 11 0.4 3 0.1 3 0.2 1 0.2 1 0.2 4 3.8 IS 3.8 5 3 1 0.6 6 6.7 108 0.5 1976 5 1.1 4 3.1 S 3.4 10 3.1 26 8.1 1 0.1 55 3.9 69 2.5 23 1.1 - 16 0.4 17 0.4 231 1.3 Redbreast sunfish 1975 14 0.3 10 0.1 8 0.3 13 0.2 S 0.3 2 0.4 4 0.7 4 3.8 117 29.5 15 8.9 10 5.2 1 1.1 203 0.8 1976 5 1.1 - - 1 0.7 6 1.5 5 1.5 4 0.4 237 16.6 189 6.7 133 6.4 - 104 2.6 23 0.5 706 4.1 Pumpkinseed 1975 30 0.7 14 0.2 8 0.3 3 0.1 S 0.3 6 0.9 2 0.4 3 2.9 14 3.S 7 4.2 5 2.6 1 1.1 97 0.4 1976 6 1.3 1 0.8 - 7 2.1 15 4.6 17 1.6 16 1.1 29 1 21 1 - 11 0.3 8 0.2 131 0.8 Largamouth bass 1975 1 (2) - 6 1.1 2 1.9 1 0.3 -10 (2) 1976 -- -- -6 1 10 0.7 1 (2) - - - "1 (2) 12 0 Tessellated darter 1975 6 0.1 16 0.2 2 0.1 1 (2) 1 0.1 - - - - - 2 1.0 4 4.4 32 0.1 1976 10 2.2 3 2.3 3 2 3 0.9 3 0.9 42 3.8 S6 3.9 14 0.5 19 0..9 48 1.2 56 1.3 257 1.5 tlmber of Species 1975 17 15 15 12 13 16 16 13 18 14 17 13 Nmber of Species 1976 16 11 10 17 17 18 28 24 18 - 19 19 (l)Not all species caught are listed, but all are Included in the totals for the number of species caught.
2
( )Less than 0.1%.
LGS EROL Page I of 2 TABLE 2.2-30 SPATIAL VARIATION IN TOTAL CATCH AND RELATIVE ABUNDANCE OF IMPORTANT SPECIES OF FISH AND TOTAL NUMBER OF SPECIES COLLECTED BY SEINE FROM TIHESCHYLKILL RIVER, 1975 AND 1976 81750 78900 78460 77960 77240 77220 77010 76840 Total Total Total Total Total Total Total Total Species(I) Year No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch No. Catch American eel 1975 0.2 Muskellunge 1976 - 1 0.1 Goldfish 1975 0.1 -
1976
- - 1 (2) 2 0.2 -
Swallowtail shiner 1975 2822 71.5 150 22.8 302 60.2 1511 51.8 885 57.5 624 50.4 620 68.8 1083 55.1 1976 179 16.3 1144 57.9 130 23.3 218 26.5 538 33.2 632 26.1 226 28 1333 49.1 Spotfin shiner 1975 1039 26.3 456 69.3 173 34.5 1032 35.4 567 36.9 546 44.1 203 22.5 808 41.1 1976 701 64 497 35.3 353 63.4 315 38.3 796 49.1 1044 43.1 315 39 1147 42.2 White sucker 1975 - 1 0.2 2 0. 1 2 0.1 - - 1 0.1 1976 73 6.7 7 0.4 10 1.8 33 4 15 0.9 136 5.6 27 3.3 6 0.2 Brown bullhead 1975 3 0.5 1 0.2 - - - 2 0.2 5 0.6 -
1976 2 0.1 - 1 0.1 3 0.2 2 0.1 1 0.1 -
Banded killfish 1975 18 0.5 8 1.2 - 21 0.7 5 0.3 10 0.8 3 0.3 6 0.3 1976 11 1 22 1.1 4 0.7 46 5.6 21 1.3 27 1.1 31 3.8 5 0.2 Redbreast sunfish 1975 18 0.5 25 3.8 12 2.4 4 0.1 23 1.5 5 0.4 21 2.3 17 0.9 1976 35 3.2 41 2.1 7 1.3 83 10.1 136 8.4 61 2.5 53 6.6 67 2.5 Pumpkinseed 1975 2 0.1 - 1 0.2 18 0.6 7 0.5 6 0.5 11 1.2 11 0.6 1976 2 0.2 3 0.2- 1 0.2 4 0.5 7 0.4 16 0.7 8 1 8 0.3 Largemouth bass 1975 - 1 0.2 2 0.1 1 0.1 1 0.1 -
6 0.7 1 0.1 1 (2) 2 0.2 -
1976 Tessellated darter 1975 2 0.3 - 2 0.2 6 0.7 11 0.6 1976 2 0.2 14 0.7 11 2 14 1.7 6 0.4 30 1.2 23 2.8 44 1.6 Nunter of Species 1975 11 15 10 18 18 19 15 17 Number of Species 1976 15 20 15 24 21 23 25 20
LGS EROL Page 2 of 2 TABLE 2.2-30 (Cont'd) 76820 76310 75730 I I I 1
Total Total Total %
Species( ) Year No. Catch No. Catch No. Catch No. TOTAL American eel 1975 - - 1 - - - - (2)
Muskellunge 1975 - - - - (2)
Goldfish 1975 - - - - (2) 1976 4 0.1 - - 7 0.5 - (2)
Swallowtail shiner 1975 1372 47.4 491 58 3566 54.8 13426 56.1 1976 1576 21.2 200 29.5 365 24.3 5611 32.5 Spotfin shiner 1975 1378 47.6 329 38.9 2728 41.9 9259 38.7 1976 1576 51.7 291 42.9 765 50.9 8000 46.4 White sucker 1975 12 0.4 1 0.1 - - 19 0.1 1976 121 4 2 0.3 19 1.3 449 2.6 Brown bullhead 1975 2 0.1 - - 4 0.1 17 0.1 1976 8 0.3 2 0.3 1 0.1 20 0.1 Banded killfish 1975 7 0.2 1 0.1 29 0.4 108 0.5 1976 41 1.3 9 1.3 14 0.9 231 1.3 Redbreast sunfish 1975 5 0.2 10 1.2 63 1 203 0.8 1976 27 0.9 51 7.5 145 9.6 706 4.1 Pumpkinseed 1975 3 0.1 1 0.1 37 0.6 97 0.4 1976 62 2 5 0.7 15 1 131 0.8 Largemouth bass 1975 4 0.1 - - 1 (2) 10 (2) 1976 2 0.1 - - - - 12 0.1 Tessellated darter 1975 2 0.1 6 0.7 3 (2) 32 0.1 1976 13 0.4 47 6.9 53 3.5 257 1.5 Number of Species 1975 19 12 17 Number of Species 1976 17 19 22 (1) Not all species caught are listed, but all are included in the totals for the number of species caught.
(2) Less than 0.1%.
LGS EFOL TAELE 2.2-31 TOTAL CATCH AND RELATIVE ABUNDANCE OF SMALL FISHES COLLECTEDCI)
FROM THE SCHUYLKILL RIVER NEAR IGS, 1973 THROUGH 1976 1973 1974 1975 1976 NQo. 1 0.1_
American eel 4 0.3 3 0.5 5 0.5 1 0.1 Goldfish 1 0.1 (2) 13 1.2 Carp 7 0.4 (2)
Cutlips minnow 1 0.1 (2)
Golden shiner 10 0.6 (2) 2 0.1 Comely shiner 14 0.9 (2)
Satinfin shiner 3 0.2 (2)
Common shiner 19 1.2 14) 7 0.5 Spottail shiner 56 3.6 1 14 1.3 45 3.2 Swallowtail shiner 155 10.1 (2) 331 31 253 17.9 (2)
Spotfin shiner 706 45. 9 43 3.9 438 30.9 (2)
Bluntnose minnow 3 0.2 (2)
Blacknose dace 9 0.6 1 0.1 Creek chubsucker 1 0.1 3 0.2 White sucker 4 0.3 9 1.5 111 1.3 16 1.1 White catfish 11 0.7 1 0.2 1 0.1 3 0.2 Yellow bullhead 9 0.6 6 22 2 11 0.8 Brown bullhead 4 0.3 1 0. 2 20 1.8 1 0.1 Banded killifish 56 3.6 Ca) 11 1 214 15.1 3
Rock bass 5 0.3 5 0.5 2 0.1 Redbreast sunfish 68 4.4 276 416.2 83 7.6 196 13.8 Green sunfish 255 16.6 1117 241.6 454 41.5 73 5.2 Pumpkinseed 54 3. .5 152 19 1.7 7 0.5 25.41 Blueqill 36 2.3 5 0.5 1 0.1 Lepomis hybrid 3 0.2 3 0.5 8 0.7 4 0.3 Smallmouth bass 1 0.1 1 0.1 Largemoutb bass 9 0.6 1 0.1 1 0.1 Black crappie 6 0.4 2 0.2 1 0.1 (2)
Tessellated darter 27 1.8 31 2.8 138 9.7 Yellow perch 1 0.1 Total 1537 598 1093 11417 (1) From aqe 0 sunfish population estimate samplinq.
(a) These species not sampled in 1974.
S LGS EROI, TABLE 2.2-32 TOTAL CATCH AND RELATIVE ABUNDANCE OF FISHES AND HYBRIDS COLLECTED (I)
DURING LARGE FISH POPULATION EST[IATE SAMPLING, 1973 THROUGH 1975 Firestone Limerick A Limerick B Vincent Pool All Sites 1974 1973 1974 1975 1973 1974 IQ75 1974 All Years Species No. .2 No. % NO. 2 No. z No. 2 No. z No. z No. 2 No. I Muskellunge - - - 1 (2) 1 - - - - - - - I (2)
Goldfish 185 8.1 113 7.3 34 6.5 247 6.7 110 7.2 44 5.8 236 5.5 196 6.1 1165 6.5 Carp 16 0,7 4 0.3 - - 20 0.5 5 0.3 2 0.3 21 0.5 17 0.5 85 0.5 Golden shiner 34 1.5 38 2.5 7 1.3 145 4.0 44 2.9 10 1.3 195 4.5 38 1.2 511 2.9 Fallfish - - 1 0.1 - - - - - - - - - - - - 1 (2)
Minnow hybrid 1 (2) - - - I (2) - - - - - - 2 0.1 5 (2)
White sucker 369 6.1 123 7.9 78 14.9 451 12.3 125 8.2 57 7.5 434 10.1 259 8.1 1896 10.6 Creek chubsucker - - - - - 12 0.3 - - - 41 1.0 - - 53 0.3 White catfish 29 1.3 15 - 8 1.5 57 1.6 I 0.1 3 0.4 37 0.9 12 0.4 162 0.9 Yellow bullhead 9 0.4 10 1.0 - - 18 0.5 - - 3 0.4 26 0.6 2 0.1 162 0.9 Brown bullhead 366 16.0 159 0.6 223 42.6 1295 35.3 222 14.5 258 33.8 1654 38.4 1103 34.5 5280 29.6 Channel catfish - - - 10.3 - - - - 1 0.1 - - - - 2 0.1 3 (2)
Rock bass 4 0.2 11 0.7 4 0.8 45 1.2 5 0.3 4 0.5 41 1.0 I! 0.3 125 0.7 Redbreast sunfish 1131 49.5 670 43.2 117 22.3 971 26.5 341 22.3 129 16.9 930 21.6 307 9.6 4596 25.8 Green sunfish 37 1.6 48 3.1 7 1.3 46 1.3 12 0.8 5 0.7 60 1.4 95 3.0 310 1.7 Pumpkinseed 71 3.1 262 16.9 43 8.2 210 5.7 596 39.0 223 29.2 384 8.9 1109 34.7 2898 16.3 Bluegill 6 0.3 27 1.7 - - 36 1.0 15 1.0 - - 87 2.0 7 0.2 178 1.0 Lepomis hybrid 5 0.2 6 0.4 - 10 0.3 3 0.2 1 0.1 14 0.3 20 0.6 5q 0.3 SaeIlmouth bass 15 0.7 5 0.3 t 0.2 to 0.3 1 0.1 3 0.4 2 (2) 2 0.1 39 0.2 Largemouth bas 4 0.2 44 2.8 1 0.2 29 0.8 35 2.3 16 2.1 44 1.0 2 0.1 175 1.0 White crappie 4 0.2 5 0.3 - - 12 0.3 3 0.2 1 0.1 44 1.0 5 0.2 74 0.4 Black crappie - - 8 0.5 - - 47 1.3 6 0.4 4 0.5 57 1.3 9 0.3 131 0.7 Yellow Perch - - 1 0.1 I 0.2 3 0.1 3 0.2 - - 4 0.1 1 (2) 13 0.1 Total 2286 1550 524 3666 1528 763 4312 3199 17828 (I) From the Schuylkill River near Limerick Generating Station.
(2) Less then 0.12.
0 tGS EROT TABLE 2.2-33 TCTAL CATCH AND RELATIVE AEUNDANCE OF FISHES CCLLECTED( 1)
DURING CATCH-PER-UNIT-EFFORT SAMPLING, JULY THROUGH DECEMBER 1976 Firestone Limerick A Limerick C Vincent A Vincent B Total Species 1o2 --L_ NO. _% EQ. AL_ Eg. A_- NO. AJ-American eel 13 2 15 1. 1 26 2.9 12 2 7 1.8 73 1.9 Goldfish 4 0.6 181 12.9 22 2.5 49 8.3 2 0.5 258 6.6 Carp 19 1.4 1 0.1 16 2.7 5 1.3 41 1 Golden shiner 1 0.2 44 3.1 6 0.7 11 1.9 204 52.4 266 6.8 Minnow hybrid 1 0.1 1 0.1 9 1.5 11 0.3 Quilltack 1 0.1 1 C2)
White sucker 205 32.1 239 17.1 - 285 31.8 141 23.9 27 6.9 897 22.9 Creek chubsucker 19 1.4; 2 0.3 21 0.5 White catfish 12 1.9 9 0.6 3 0.3 2 0.3 26 0.7 Yellow bullhead 10 1.6 12 0.9 20 2.2 4 0.7 6 1.5 52 1.3 Brown bullhead 57 8.9 302 21.6 60 6.7 40 6.8 25; 6.2 483 12.3 Channel catfish 1 0.1 1 (2)
Rock bass 4 0.6 11 0.8 17 1.9 3 0.5 2 0.5 37 0.9 Redbreast sunfish 279 43.7 204 14.6 240 26.8 112 19 19 4.9 854 21.8 Green sunfish 10 1.6 85 6.1 58 6.5 23 3.9 18 1..6 1951 5 Pumpkinseed 17 2.7 166 11.8 115 12.8 122 20.6 57 14.7 477 12.2 Blueqill 1 0,2 7 0.5 7 0.8 8 1.4 1 0.3 24 0.6 Lepomis hybrid 11 1.7 9 0.6 9 1.5 6 1.5 35 0.9 Suallmoutb bass 11 1.7 2 0.2 5 0.8 1 0.3 19 0.5 Larqemouth bass 1 0.2 22 1.6 18 2 2 0.3 3 0.8 46 1.2 White crappie 5 0.4 2 0.2 2 0.3 1 1 13 0.3 Black crappie 28 2 6 0.7 16 2.7 3 0.8 53 1.4 Yellow perch 2 0.3 21 1.5 6 0.7 3 0.5 32 0.8 Walleye 1 0.1 1 (2)
Total 638 1.01 896 591 389 3915 (c) From the Schuylkill River near Limerick Generatinq Station cz) Less than 0.1%
LGS ERCI TABLE 2.2-34 FISHES TAKEN BY TRAP NIT FROM THE SCHUYLKILL RIVER AT VINCENT POOL FROM MAY 1971 TBRCUGH DECEMBER 197E 1971 1972 1973 1974 1975 1976 TOTAL AWL % -Ro % _Q., _.L ,o. % --&-Z . No. __ NO (1) (I) C1)
Bowf in 1 1 1 (1) 1.6 3 American eel 8 0.2 5 0.2 114 0. 3 I5 0.4 55 97 0.5 Goldfish 9 0.2 10 0.3 314 0.7 1835 4.7 35 3.8 25 0.7 298 1.5 Carp 12 0.3 6 0.2 7 0.1 6 9.2 5 0.1 36 0.2 Golden shiner 10 0.3 8 0.3 48 1 40)9 10.3 6 0.6 57 1.6 538 2.7 Spottail shiner 9 0.3 19 0.4 6 0.2 20 2.2 23 0.7 77 0.18 Swallowtail shiner 2 0.1 10 0.3 16 0.3 1 CI) 1 0.1 30 0.1 Spotfin shiner 1 (1) 5 0.1 6 CI)
Cl)
Minnow hybrid 2 0.1 2 Quillback 1 (') 4 0.1 4 0.1 9 C1)
White sucker 21 0.5 21 0.7 97 2 817 2.2 19 2.1 60 1.7 305 1.5 Check chubsucker 2 0.1 1 (1) 1 CI) 4 (C)
White catfish 22 0.6 44 1.5 94 -2 6S5 1.6 148 5.2 73 2.1 346 1.7 Yellow bullhead 5 0.1 1 CE) 2 (1) 3 0.1 1 0.1 8 0.2 20 0.1 Brown bullhead 1496 38.3 1127 37.5 1309 27.4 99 1 25.1 287 31 615 17.5 5825 29 Channel catfish 4 0.1 10 0.3 15 0.3 3 14 0.9 6 0.6 10 0.3 79 0.4 Margined madtom 1 (I) 1 (S)
Rock bass 21 0.5 114 0.5 .15 0.3 25 0.6 13 1.4 51 1.*1 139 0.7 Redbreast sunfish 57 1.5 71 2.4 138 2.9 16 2 4.1 75 8.1 538 15.3 1041 5.2 Green sunfish 113 2.9 20 0.7 75 1.6 15.3 3.9 19 2.1 243 6.9 623 3. 1 Pumpkinseed 1932 49.14 1449 48.2 2527 52.8 147 1 37.2 298 32.2 1265 35.9 8942 44.5 Blueqill 15 0.4 73 2.14 119 2.5 8i1 2 31 3.3 105 3 424 2.1 Lepomis hybrid 3 0.1 15 0.5 23 0.5 2'9 0.7 8 0.9 118 3.14 196 1 Smallmouth bass 1 Ci) 2 0.1 3 (I) tarqemouth bass 2 0.1 1 CI) 8 0.2 11 0.1 White crappie 1;6 3.7 68 2.3 171 3.6 13 6 3.14 32 3.5 66 1.9 619 3.1 Black crappie 31 0.8 39 1.3 59 1.2 85 2.1 27 2.9 163 4.6 494 2 Tessellated darter 1 (I) 1 (1)
Yellow perch 3 0.1 18 0.5 21 0.1 Total 3909 3005 4784 3956 926 3520 20100 C)Less than 0.1%
LGS EROL TABLE 2.2-35 CRITERIA FOR DETERMINING OF IMPORTANT FISHES OF THE SCHUYIKI-I. RIVER
-IMPORTANCE
- LINK TO PLANT DIRECT Susceptible Susceptible Susceptible to to to ComonName Commercial Recreational Ecological Abundant Ipngement Entrainment Discharge American shad' 2 x x x 'C American eel x x XI x Muskellunge x Goldfish2, 314 x x K x x Swallowtail shiner 4 ' s x x x 'C x Spotfin shiners x x x x x White sucker 2 ' 3 1, x x x x 'C Brown bullhead21 316 x x x x x Banded killifish x x x Redbreast sunfish2 '316 x x x 'C x x 2
Pumpskinseed f 316 x x x x x x Largemouth bass x x x Tessellated darter x x a x I Importance of species largely dependent on results of Pennsylvania Fish Commission program to provide fishwavs at dams downriver of LGS.
2 Species samples by large fish catch-per-per-unit-effort program.
3 Species sampled by large fish population estimate program.
4 species sampled by push-net program.
s Species sampled by seine program.
6 Species sampled by age and qrowth program.
LGS EROL TABLE 2.2-36 SPATIAL AND TEMPORAL VAPIATION IN CATCH-PER-UNIT-EFFCRT (N0.1MIN OF ELECTROFISHING X 100) OF IMPCPRANT SPECIES COLLECTED FROM THE SCHUYLKIIL RIVER NEAR LIMERICK GENERATING STATION, JULY THROUGH DECENER 1976 Common Name/ Limerick Limerick Vincent Vincent American eel Jul 18.81 2.08 14.89 5.58 1.75 Auq 0 2.23 5.41 3.37 1.52 Sep 2.22 8.29 6.09 0 1.52 Oct 0 2.08 0 3.57 0 Nov 4.04 2.96 6.44 1.25 4.00 Dec 0 0 0 0 1.45 Goldfish Jul 0 22.39 7.26 13.70 1.75 Auq 3.51 29.83 2.38 1.09 1.04 See 3.03 21.98 4.38 3.77 0 Oct 0 29.72 8.03 18.70 0 Nov 0 53.11 4.17 8.85 0 Dec 0 45.51 4.10 12.76 0 White sucker Jul 10.71 4.35 7.32 8.06 0 Auq 82.22 14.26 22.87 31.21 1.96 Sep 93.57 58.96 78.31 29.50 3.51 Oct 115.75 83.20 106.80 62.73 5.09 Nov 96.57 68.36 122.42 28.27 5.56 Dec 69.94 64.21 56.99 13.26 22.11 Brown bullhead Jul 57.94 11.00 25.04 7.38 0 Auq 37.87 25.80 25.16 20.97 0 Sep 4.79 23.05 16.93 3.59 1.75 Oct 0 12.86 4.61 11.09 8.34 Nov 16.18 163.78 3.91 4.42 14.44 Dec 2.22 74.30 2.78 0 8.81 Redbreast sunfish Jul 167.50 7.43 17.59 1.19 1.70 Auq 133.53 24.08 53.96 9.05 5.88 Sep 140.00 39.91 100.96 48.94 10.29 Oct 62.18 139.56 107.54 62.45 11.68 Nov 62.23 47.08 35.75 17.02 0 Dec 20.82 18.55 13.70 9.11 0 Pumpkinseed Jul 6.83 3.13 9.89 5.74 18.30 Auq 9.59 16.82 50.21 12.67 8.09 Sep 15.76 17.83 65.92 40.64 12.04 Oct 0 47.95 9.60 38.71 33.54 Nov 0 74.87 6.80 33.85 9.78 Dec 0 29.72 9.75 14.66 6.96
LGS ERCL
'IABLE 2.2-37 ESTIMATED NUMBER AND BIOMASS OF SELECTED IMPORTANT SPECIES CCLLECTED FROM THE SCHUYLKILL RIVER DURING LARGE FIS8 POPULAIION ES7IMATE SAMPLING, 1973 THROUGH 1977 iestn ~ Limerick.h Limerick Yean Lim~erick Vincent Pool Yea No kqLt N2Lbb kqh N/h k/ No/ha k3t/fl 6o/ba k32i9 Goldfish 1973 326 73.24 1974 195 nct 1975 161 34.86 120 28.42 140 31.64 1977 259 54.81 212 56.53 544 91.444 378 73.99 167 32.98 Mean 227 187 45.70 332 59.93 281 59.62 White sucker 1973 324 80.70 1974 300 nc 144 nc 1975 239 45.00 168 30.42 203 37.71 1977 384 56.96 145 23.23 341 49.12 243 36.18 220 32.14 Mean 342 192 34.12 255 39.77 257 51.53 182 Brown bullhead 1973 566 95.12 1974 231 nc 1868 nc 1975 517 50.53 558 88.13 537 69.23 1977 46 6.10 152 34 .93 158 36.22 155 35.58 1068 207.47 Mean 139 335 42.73 358 62. 18 419 66.64 1468 fledtreast sunfish 1973 271 10.22 239 9.14 255 9.68 1974 377 nc 134 nc 1975 341 10.55 237 8.59 289 9.57 1977 723 22.37 494 18.83 283 10.99 389 14.91 345 8.20 Mean 550 369 13.20 253 9.57 311 11.39 240 Pumpkinseed 1973 79 3.22 223 9.73 151 6.48 1974 445 nc 1975 59 2.12 127 4.80 93 3.46 1977 28 1.34 91 4.68 60 3.01 81 3.65 Mean 55 2.23 147 6.40 101 4.32 263 Inot calculated
LGS ERCI TABLE 2.2-38 MEAN CALCULATED PO*K LENGTH AT ANNULUS FOR SELECTED IMPORTANT SPECIES COLLECTED FROM THE SCHUYLKILL PIVER NEAR LIMERICK GENERATING STATION, 1973 THROUGH 1975 N~o. o f I=x Specimns YVrSAMUTC. 52CCMt AMMER* A-12 I at ME tn..1 I..L II =i IV V V.I ML Goldfish 1974 Ccmbined 45 113 190 White sucker 1973 Limerick A 126 87 190 214 Limerick 2 172 98 204 279 303 Cowibine~d 298 93 198 258 303 Brown bullhead 1973-74 Combined 351 91 141 179 209 239 258 264 1975 Combined 81 103 155 194 222 251 276 Redbreast sunfish 1973 Ccmbined 516 42 94 131 145 159 1975 Combined 88 37 89 115 110 Pumpkinseed 1973 Limerick A 109 51 90 103 Limerick 9 228 50 98 124 Combined 337 51 95 121 1975 Limerick A 23 44 94 116 Limerick B 43 39 90 106 Combined 66 91 111 Larqemouth bass 1973 Combined 17 90 126 242
LGS ERCL
'TABLE 2.2-39 LENGTH-WEIGHT RELATIONSHIPS( 1) FOR SELECTED IMPORTANT SPECIES COLLECTED FROM THE SCHUYLKILL RIVER NEAP LIMERICK GENERATING STATION, 1973 THROUGH 1978 No. of Common Name Limeritck Specimens a b Goldfish 1975 Limerick A 12 - 9.93 2.88 Limerick B 29 - 9.04 2.71 White sucker 1973 Limerick A 62 -10.24 2.82 Limerick F 66 - 9.47 2.69 1976-78 Combined( 2 ) 2,034 -11.16 2.99 Brown bullhead 1973-74 Combinedc3) 564 -10.62 2.90 1975 Combined( 3 ) 97 - 9.84 2.74 Combined(2) 1,349 -11.54 3.08 Redbreast sunfish 1973 Combined(3) 345 -10.33 2.93 1975 Combined ( 23 88 -11.12 3.09 Combined( ) 1,621 -11.70 3.21 Pumpkinseed 1973 Limerick A 124 -10.28 2.95 Limerick B 31 - 9.18 2.72 1975 Limerick A 23 -11.73 3.23 Limerick R 43 - 7.26 2.30 (1) i W = a+b In FL.
(2) Sites Limerick A, B, C and Firestone.
( 3) Sites Limerick A and B.
IGS ERCL TAEIE 2.2-40 (Page 1 of 2)
NUMBER OF SAMPLES BY YEAR, FPROGRAM, AND SITE COLLECTED FROM PERKICNEN CREEK, 1972 THRCUGH 19771(1)
Program/Sites 19%2 1973 19714 1275 1976 1977 Water Quality P18700 - 24 P14390 14 24 24 24 Phytoplankton P14390 -11 Periphyton P14390 14 Benthic Macroinvertebrates P22000 12 12 9 11 P13600 10 12 9 11 Macroinvertebrate Drift P14390 12 84 72 Larval Fish Drift P14390 479 514 504 696 Larval Fish Trap P14390 84 240 Seine P19775 - 11 11 P16500 - 11 11 P14455 - 10 10 P14320 - 10 11 P14130 - 11 11 P13580 - 11 11 Small Fish Population Estimates P14830 3 P14690 3 3 P14585 3 P14225 3 3 P14210 3 3
LGS ERCL TAEIE 2.2-40 (Cont'd) (Page 2 of 2) 1972 1973 1974 1975, 1976 1977 Larqe Fish Population Estimates P20000 4 P19765 2 P14390 5 5 P14160 3 2 3 P14020 2 2 Aqe and Growth P20000 White sucker 49 Redbreast sunfish 64 P19860 Redbreast sunfish - 51 Green sunfish - 30 Smallmouth bass - 9 P17400 Redbreast sunfish - 50 Smallmouth bass - 28 P14390 White sucker 33 Redbreast sunfish 53 65 Green sunfish 32 Smallmouth bass 40 P14160 White sucker - 46 Redbreast sunfish - 64 P14020 White sucker - 36 Redbreast sunfish - 56 P13580 Redbreast sunfish 77 Green sunfish 41 Smallmouth bass 5 (Vsee footnotes in Table 2.2-72 for the definition of what constitutes one sample.
LGS ERCI TABLE 2.2-411 NUMBEP OF SAPLES BY MONTH, PROGRAM, AND YEAR COLLEICTED FPCH P!RKICMEN CREEK, 1972 THROUGH 1977 1,2 Prog am Az J7an ,k LI Miz =iu~x W gw L1 An9 .iD *g= I~y Lec Water Quality 1974 2 2 2 2 2 2 2 1975 2 2 2 2 2 2 2 2 2 2 2 2 1976 2 2 2 2 2 2 2 2 2 2 2 2 1977 14 4 4 14 14 14 14 4$ 14 4 4 4 Pbytoplankton 1974$11 Periphyton 1973 - --- 1 3 £4 2 2 Benthic Macroinvertebrates 1972 1 2 2 2 2 2 2 2 2 2 2 1 1973 2 2 2 2 2 2 2 2 2 2 2 2 1974 2 2 2 2 2 2 2 2 2 1976 2 2 2 2 2 2 2 2 2 2 2 Macroinvertetrate Drift 1972 12 12 1973 12 12 12 12 12 1974 12 12 12 12 12 12 Larval Fisb Drift 148 1973 96 120 95 96 214 1971$ 4$7 1411 114 1014 105 1975 l144 72 144" 1144 1976 72 132 132 141 216 Larval Fish Trap 1975 . . .- - 214 12 21$ 214 . ...
1976 - - - 214 48 48 118 72 . . ..
Seine 1975 - 4 6 6 6 6 6 6 6 6 6 6 1976 - 6 6 6 6 6 6 6 6 6 6 5
'See footnotes in Table 2.2-7 for definition of what constitutes one sample 2Number of samples for Small Fish Population Estimate, Large Fish Population Estimate, and Aqe and Growth proqrams was not included because only annual data was utilized.
LGS EROL TABLE 2.2-412 (Paqe I of 2)
MONTHLY QUALITATIVE LISTING OF PBYTCPLANKION GENERA CCLLECTED AT P14390 IN PERKIOMEN CREEK IN 1974 A2~fJan 14 .1+/-4M 1 AID.R a 23 31 jul 29 Au 20 Se 18 cct 21L N 12 Dec Chlorophyta Eudorina X(t) X x Pleodorina C x
Chlorococcum x X x x x x C C C K x Kirchneriella x x x x Se lenast ru x 00ocst is x K x x
Coelastrum x Scenedesmus x x A C x x Hyd rod ict vo x Pediastru Ulothri x x x x X x x C X x x x x x
stigeocloniwn x x x Oedoconi x x Cladophora x x
x x x X X X K x x x Ceerinu K x x Csarium~za x I x x x x x x x x K K x X x x x x X svaurastu K
Merosium x Maflliona x X x x x x
Caigicus CXSlotell x x x x x C X x x
x x K x x A C C X Meloirafl A xx Stepanoi c x X x x x K X X x X X x x x x x X X X C
0 LGS EROL TABLE 2.2-142 (Cont Id) (Page 2 of 2) 25 a 4Fe 1 MaE iAyrISk 23 Ma 3~Jul 29 Au 20 SeD 1Sct 21 Nov Bacillariophyta (cant.)
'C 'C 'C 'C 2bierido x IC Synedra x x x 'C x 'C x x 'C 'C Tabellaria x 'C
'C 'C 'C x Cocconig 'C 'C x 'C Naicl 0x x x 'C x 'C C 'C A A A
'C 'C x
'C x 'C 'C x X
x x x x x 'C 'C x C 'C 'C Rhai coanphenia 'C SurirellaU X I x 'C Cvanophyt a Coelosnhaerium X Osclltoiax x x 'C A X
'C (1~) X = present, C =common, A = abundant
IGS EROI SABLE 2.2-43 PERIPHYTON PPCDUCTICN LISTED AS TCIAI BICMASS (STANDING CPCP) MG/DM2 AND TOTAl PRODUCTIVITY RATES MG/EM2/EAY. (1)
Exposure Mean Ash-free Accumulation Production Date Time (days) 5Wt. (rq/dWr'l (I9/dm 2 /dav- t) 17 Auq 10 58.7 24 Auq 17 80.9 22.2 3.17 31 Auq 24 73.0 - 7.9 -1.13 7 Sep 7 74.2 14 Sep 14 98.3 24.1 3.44 21 Sep 21 23.8 -74.5 -10.64 5 Oct 7 34.5 12 Cct 14 90.7 56.2 8.03 19 Cct 21 105.7 15.0 2.14 26 Oct 7 18.1 - 5.5 -0.79 2 Nov 14 12.6 9 Nov 21 29.8 17.2 2.46 12 Dec 12 4.2 19 Dec 19 3.2 - 1.0 -0.14 (1) Values (ash-free dry weiqhts) are listed fcr station P14390, Perkiomen Creek, Durinq 1973.
9 LGS ER V TABLE 2.2-4 4 (Page 1 of 3)
SPECIES LIST AND RELATIVE CU*LITATIVE ABUNDANCE OF MACRCINVERTEBRATES COLLECTED BY ALL METBODS FROM ALL HABITATS IN EAST BRANCH PERKICMEN CREEK AND PERPIOMEN CREEN, 1970 THROUGH 1976 (I)O(2)
POP IFERA ARTHPOPODA (cont'd) APTBRCPCDA (cont'd)
Sponqillidae (U.28) Ampbipoda Ephemeroptera (cont 'd)
COELENTEPATA ¶alitridae Heptaqeniidae (cont Id)
Bvalella azteca (U,28) Stenonemf fuc.num (PR.22)
PLATYHELXINTHES Gamnaridae *. evotellum (C, 22)
Plaqiostomikbe Gammarue fasciatu (U,28) g.
- .rubropacul.ptu (R,22) rutr1* (C,22) liydroJ..MI 2Zris (U, 21) Cran2ogxM acil (R, 28)
Planariidae .St&yonecte$ op. (R,19) .§. v caL*um (R. 22)
DugeinJa dorotocevbajLa (A,21) Cecapoda S. WIunctatu m (t,22)
J2. +/-.LgLLM (U,211 Cambaridae 1. smithae (P,22)
NFEXERTEA Cambarus bartoni (C,28) Odonata Pxostomo arec (C, 15) Orconectes limosus (C, 28) Gamphidae NEMATODA (0,.12) Hydracarina (C, 28) GmipbU guadricolor (R.26)
BRYOZOAL Collembola Lantbu albistylus (0,26)
Isotomidae Libellul ida° AMNLIDA Isotoma op. (C,28) Platbemis lydia (CK26)
Oliqocbaet a Isotomurs valustris (C,28) Leucorrxbnia sp. (R,12)
Lumbricidae (U,21 Poduridae Peritbemis op. (R,26)
Tubificidae Hymoaastrura sp. (V,28) Libellula op. (.R26)
Liunodrilus k fmeinstsr (C.,2) Suinthuridae (0,28) Nacromuidae 1,. claparedianus (U,2) Epbemeroptera Macromia allabaniengi (C,26)
~BralIcim sowrli (U, 2) Ephemeridae Corduliidae Peloscole £ne2 (U,2) Eybemera imulang (P,6) Evicordulua orincevs (P,26)
Aulodrilu limnobius (U,12) Caenidae weuroqrdul obsoleta (R,12)
Aeolosomatidae (U. 2) aenis op. (C, 12) Calopterygidae Naididae Tricorytbidae Calorteryz op. (P,12)
Trioorvtbodes p. (C, 12) Coenaqrionidae Pril3tin brvsexzIL (U,18) Epbemerell idae Argi app. (C,12)
Ekhegerella Enallagma app. (P°12) 2.f+/-n* (U+/-n.18 (.18 Z. attenuata defign (0,G)
(C, 6)
Ischnuaa spp. (V,12)
Lumbriculidae (AZ2) 1.-dorothea (U,6) Aeschnidae Branchiobdellidae (U,21 Leptophlebiidae Baaiaescbna lanata (P,28)
Hirudinea Paraleytopblebia rraeedit (V,6) Aescbna sp. (U,12)
Glossiphoniidae ChoroteXMe basalis (U,6) *AM Junius (U,26)
Eaetidae Plecoptera
- j. ineto (P,321 Raetis iontercalaim (A,6) Taeniopterygidae B. oignnt (R,32) B. frondai Z (R,6) Stroybocteryx faciata (R,35)
R. ~g~rasit (U,32()32 j- £ *fs~~I (V,6) aeioD teryx Divalis (C,35)
- 1. f (Po6) Capniidae Actinobdell triaDDJulat. (P,*32) Alloca nia vivivara (C,35)
Batgacobdella Rbaler~ (P,321 A. namaea (U,35)
Piscicolidae Ameletus lineatu (R, 6) A. xickeri (0,35)
Piecic.iaria xrIiauk. (R,241) Pseudocloeon m (C,6) Nemouridae ringiggl milner (R.241) .f. punctiventris (0,6) Amnbinemura delosa (C,35)
Erpobdellidae Hlerocleo curicu (C,6) Perlidae Erodel junctata (C,321 Cloeon al&marnc (0,6) N*eoerla clvyene (U, 35)
Bir udinidae Centroptilu sp. (PF6) Pbasaanopbor capitata (R,35)
HaiMnfvi. marmorLat~a (P.32) Siphlonuridae Perlesta placida (C.35)
Sithlon*fur sp. (P,6) AgronejujK ajnj~j (P,35)
ARTHROPODA Ilsnycbia sa. (C,6) Leuctridae Isopoda Heptaqeniidae leijotra op. (R#35)
Ascii idae Bectauenia sr. (R.6) Perlodidae Asellu~ conununis (C,38) Stenonegna (=enjAjogD) (0,22) TjsEeX a I*_lleata (C,35)
A&. st.ius (R,7Rl intercunctatum 1bpterntarRa lp M11lnrnW0-1 iAtia 1tP-l;
LGS ERCL TABLE 2.2-414 (Cont'd) (Paqe 2 of 3)
AFTBROPODA ARIIIPCPCDA (cont' d) APMRTIUOCA (ccnt 'd) liemiptera Coleoptera (cont'd) Tricboatera (cont 'd)
Gerridae Bydrophilidae (cont 'dl Leptoceridae gerrit remia's (C,7) .T. lateralis (C, 11) Ceraclea trangverea (R.29)
Metrobates jguagmaus (C,71 anacaena linibata (C9 11) g. sp. A (U,39)
Bheumatotates rie (C,7) Sphaeridium spp. (U, 37) Cecetis spp. (U,31)
Treixilates M~bnitJgus (C,7) Hydrobiuu melagn (PR.11) MyStacides seulcbralis (R,31)
'Jeliidae Hydraenidae Triinsd sr. (R,31)
Th*2aveliJJ op. (C,28) Hydraeri up. (U,,37) Hydropsycbtidae Ocbhtb~bius sp. (U,37) Cheumatcvsvcbe art. (A,31)
C or ixid ae Hydroscaphidae Hvdrovezcbe betten (0,31)
Hyrcrscacha natanj (PR,37) *.cbalerata (R,31)
Puephenidae up. A (C,39) s.
Zeepengsa berrikI (C,31 s* B (P,39) up.
Saldidae Eubriidae up. C (A,39) o-up.
- o. C (U,39)
Pentacox up. (U,37)
Dryopidae .Q up. E (C,39)
Notanectidae Macronema ej34atym (C,31)
Noto.nge.I op. (P.28) Elmidae Diglectron modesta (P,31)
Belostomatidae Anyoy varieaata (R,33) Hydroptil idae belosto~mI sp. (R,37) DubiakiZ~Dia vittata (C, 3) BydroutJ*LlA.jax (0,31) tNeqaloptera .9. bivittata (U,31 M. consimiljj (C,311 Sialidae .P. guad-riDngtat (P,,3) uuatulata
- o. (C.31)
Sitali sp. (C,28) Microcvllorue yujjjlj (C,33) . uat (U,31)
Corydalidae g. ffliyj (R,3(C)3 j. 5aubeslana (P,31)
C~x.vdiia corn.u+/-t (C,26) Lectrc iavctinee (A,31)
Niarggnia nserricrni (R,27) il.earnele cren~ta (A,3) Auravle. op. (R,31)
Coleoptera 1. op. B (R,39) 9Oxyetbize o. (F,12)
Haliplidae .Macrnvbu glAbratue (R,33) LepidoFtera
,R mgticu~ (U,1) .3ulimni3v l*+/-+/-1Escl1r (P.33) Pyralididae Cbrysowelidae Parargvractis sp. (C,37)
Haliipiaus fnLagiatu (P,ll Galerucella nuurkhaeae (D,11) Diptera Dytiscidae Dona~ia vincetrix (P,11) Tipulidae
?4europtera Ls2Ekil up. (R,37)
Iyius~gM sp.tia (P.113 Sisyridas sop. (R,37)
VirnoasD. (P, 37)
Miaabzu gJjgjljp (C.11 Erioztera. sp. (U,37) lrichoptera Arrtogba sp. ('U,37) fi.sp. A (R,391 Glosoosomatidae Hyryau op. (R,28) Glossoeoma sp. (R,31) Poeudclimnolcla up. (t:,20)
Bbyacophil idae Limni~ai op. (R,37)
C22eltu ayD1icua (p,11) Paradelyhomvia sp. (R,37)
Gyrinidae fbilopotamidae Dolicbomeza op. (P,37)
Qimarra obscura (A,31) Tivul upp. (U,37)
D1ineus hogni (P*11) S. aterrisa (U,31) Siwuliidae Wormaldia m22stu (U,311 Siulu jttaj],m (A.,34)
Hydrophilidae Psychomyiidae Prosivulium op. (U,37)
Cbironoridae
- 11. sp. A (R, 14). 1imctgoint3l dvari ],P30)
PolycentroRMs op. 0,194) Tanvvuy sr. (R,23)
Z. cinctus (C,251 Procladiu* xi aris.*l IT,30)
Pbryqaneidae A.labesulvia arienis (U,30)
Laccobius agilis (C,111 Ptilostomis op. (B.311 Pentaneurini spp. (A,23)
Limnephilidae 7anytarsini (A) includinq Ileouhylax sp. (R,131 Hicroysectra mundeneis 120)
a 4 LG L TABLE 2.2-44 (Contel) (Paqe 3 of 31 ARTHROPODA (cont'd) APTHPOPODA (cont'd) AR-THROPCbA (cont'd)
Diptera (cont'd) Diptera (cont'd) Hymenoptera Chironomidae (cont'd) Chironomidae (cont' d) Diapriidae Tanvtaroun exiga (30) eterotriesocladlju up. (0,23) (R,37) s*icbgnria or.
T. agfeLr (30), and Ihienemanniella sp. (R.23) Mymaridae T. alabrescens (30) Psychodidae Caravhractus sp. (0,37)
Pseudocbironomus yl zjg (R,30) Fsychoda sp. (0,20) MOtLUSCA Chir2nomu app. (C,23) sop. (R,.20) Gastropoda Crvvtochironomus S:. sorex (Uol0}
fujj (0,30) TelmatoscoD*8 up. ((R,20) Physidae Heleidae Thxi sacta (A,9)
C. blarin (U,10) P9lpomvia Opp. (C,37) Lymnaeidae.
Endochironomus sp. (0,23) -Da ep. (R,137) Lyta A bumili (C,16)
Irib j sp. (U023) Atrichovoaon vgriOM (It.36) P1 anorbidae Dicrotendi=e motag (U,30) ,yal vary (C, 16)
A. op. A (VR39)
Gi*taotendiae sp. (0, 23) A. op. B (P,39) IHli.soma tjygoy (R,16)
Polyeinluim illipoens (A0 30) St,,obezzji op. (P,36) L3. anger: (R,16)
,. falu (R,20) up. (R,36) sliggidqq Ancylidae Ferrisgtard (A, 16)
Paraclad-oelma sp. (R,23) Rmpididae gicrotediJ23 tasl (C,301 up. (0°37) 8 Viviparidae Paralauterborniella op. (R,231 lin dmi sp. (C,37) Ca lMj decis (R16)
Paratendives sp. (0,23) Ephydridae Pleuroceridae Stictochironomuw up. (U023) Brachydeuternagenta: a (R,37) .noasi v ic 1,416)
Stenochironomus op. (U,23) Scatejla-Nesjae~ll up. (P,437) Bydrobiidae Parac8ironomu op. (U. 23) Culicidae Ampncola limes (0,16)
Pbaenopye2=a up. (0,23) A2~bore3 op. (R4.37) Valvatidae Xenochironomus xeno Jj (R,30) Anopheles up. (R,20) Valvata ydcnl (P,16)
Diames ivor~und (U. 30) Muscidae Pelecypoda
£iocladius obscuru (C. 30) L*s1 op. (0,20) Sphaeriidae Criatopfl kintu (A. 30) Mycetophilidae (1,20) Wbsculium securis(R, 5)
£. sp. 1 (R,30) Dolichopodidae Other C app. (C, 23) Anhrosylus up. (R120)
M. stitn (P,S) xiidionp. (K,5)
Ohtbgiladius gigum (U, 30) Taba nidae Eukiefferiells pp. (0,23) CIr1sove sp. (U,20) Unionidae Tricbocladius op. (0,23) Tauanu op. (R,20) Anodonta cataract£ (V.8)
Dit)lo.uaiu j (U,30) Sciomyzidae A. imbecilis (14,11)
Psectrocladi op. (0,23) Dictva sp. (R,137)
Brilli sp. (P,23) Stratiomyiidae (R, 371 Ligarei. Dtas2 (RIB8)
Metriconeus sp. (R,23) Rhaqionidae Cxnonzs xena (R,30) Atberix varieqata (R,37)
(1) A - abundant, C = common, U - uncommon, P - rare.
(2) Numbers refer to the taxonomic references listed below. For complete citation see the literature Cited section.
- 1. Briqham (Ref 2.2-63) 15. Gibson and Moore (Ref 2.2-65) 28. Pennak (Pet 2.2-37)
- 2. Brinkhurst (Ret 2.2-18) 16. Harman and Berg (Ref 2.2-28) 29. Resb (Ref 2.2-71)
- 3. Browm (Ret 2.2-19) 17. Hilsenhoft (Ref 2.2-66) 30. Roback (Ref 2.2-38)
- 4. Burch (Ret 2.2-20) 18. Hiltunem (Ref 2. 2-67) 31. Poss (Fef 2.2-39)
- 5. Burch (Pet 2.2-21) 19. Holsinqer (Ref 2.2-31) 32. Sawyer (Pet 2.2-40)
- 6. Burks (Pet 2.2-22) 20. Johannsen (Ref 2.2-68,69) 33. Sinclair (Ref 2.2-72)
- 7. Calabrese (Pers. Comm.) 21. Kenk (Pers. Comm.) 34. Stone (Pef 2.2-11)
- 8. Clarke and Berq (Ref 2.2-23) 22. Lewis (Ref 2.2-33) 35. Surdick and Kim (Pet 2.2-42)
- 9. Clench (Pers. Comm.) 23. Mason (Ref 2.2-34) 36. Thorsen (Ret 2.2-73)
- 10. Curry (Ret 2.2-64) 24. Meyer (Ref 2.2-35) 37. Usinger (Ret 2.2-44)
- 11. Dillon and Dillon (Ref 2.2-24) 25. Miller (Pers. Comm.) 38. Williams (Vef 2.2-45)
- 12. Edmundson (Ref 2.2-25) 26. Needham and Westfall (Pef 2.2-36) 39. Consultant's desiqnatcr
- 13. Flint (Ref 2.2-26) 27. Neunziq (Ref 2.2-70) 10. Bobb (Pef 2.2-74)
- 14. Flint (Ref 2.2-27)
LGS ERCL TABLE 2.2-45 (Paqe 1 of 2)
SELECTED MEASUREMENTS FOR TOTAL MACRCBENTHCS IN THE RIFFLE BIOTOPE OF PERKIOMEN CREEK AND EAST BRANCB PERKIOMEN CREEK (1972-1976)
Mcrisitas Index Ncrisitas Index of Overlap(2) of Overlap 1972 Total Adjacent With Moyer 1973 Total Adjacent Uitb Moyer wt.*/mj* C ) Taxa Statigns Station Wt./m2 Taxa Stations Station East Branch Elephant 4716.7 51 0.4138 5771.9 2.4953 58 0.349 0.535 0.575 Branch 6599.8 61 0.556 11371.0 1.5017 55 0.597 0.594 0.555 Sellersville 5958.6 43 0.539 5986.1 1.6511 55 0.512 0.592 0.672 Cathill 6499.2 28 0.462 2751.7 0.3097 25 0.513 0.462 0.513 Mover 7545.2 42 n/a 7836.1 1.9451 42 n/a 0.785 0.701 Wawa 12497.7 46 0.785 11706.7 3.6821 50 0.701 0.640 0.602 Perkiomen Rahne 11980.4 61 0.566 10599.6 4.0538 65 0.498 0.691 0.742 Spring Mount 8261.3 67 0.7141 14301.1 4.2128 73 0.651
0 IGS EROC TABLE 2.2-45 (Cont'd) (Paqe 2 cf 2)
Morisitas Index Mcrisitas Index of Overlap(g) of Overlap 1972 Total Adjacent Uitb Moyer 1973 Total Adjacent Witb Moyer Wt./ME( ) Taxa Stations Ut.LDL Taxa Stations Station East Branch Elephant 6066.7 2.3133 64 0.5400 6390.5 1.7840 63 0.282 0.413 0.300 Branch 7444.4 2.2460 49 0.576 79541.8 2.63547 554 0.663 0.669 0.3548 Sellersville 8669.2 2.2199 53 0.489 125493.2 4.7003 58 0.502 0.685 0.270 Cathill 0.9791 5308.6 28 0.478 11753.54 3.36542 545 0.249 0.478 0.249 Moyer 13871.9 5.7547 44 n/a 304*46.6 7.6905 54 n/a 0.543 0.670 Wawa 20354.7 6.1566 44 0.543 50565.2 14.14593 149 0.670 0.440 0.490 Perkiomen Rahns 115433.9 3.0759 61 0.5495 17612.5 4.4454 65 0.518 0.75454 0.731 Sprinq Mount 16018.9 3.50754 71 0.718 21404.5 5.3368 61 0.689 CI) Biomass is expressed as q dry weight.
cz) Morisitas index of overlap, a measure of bentbic community similarity between stations, computed excludinq chironomide.
0 LGS EPOL TABLE 2.2-46 MEAN DENSITY (NO./mZ), PERCENT COMPCSITION (%), AND FREQUENCY OF OCCURRENCE (FO %) OF BENTHIC MACROINVERTEBRATES (I) COLLECTED IN QUANTITATIVE SAMPLES (1972-1976) FROM THE RIFFLE BIOTCFE OF EAS7 BRANCH PERKIOMEN CREEK, ALL STATIONS COMBINED 1972 1973 19741 1976 No./m2 _J F0 No.o / L O %2 No, /m FO no /MED!
.Dag&ej. spp. 99.3 Ca) 37.4 39.9 (a) 31.5 379.2 3.7 51.9 1133.6 5.6 63.2 181.1 2.5 36.5 197.3 2.6 37.1 205.6 (2) 54.6 289.4 (2) 414.41 Baet~is spp. 282.2 3.8 68.7 318.7 4.2 72.9 676.9 6.6 88.9 2373.4 11.8 93.1 Chiaiwrx app. 697.9 9.5 48.1 571.1 7.5 50.2 1005.4 9.8 71.3 1836.1 9.1 68.2 C~heumgtopssche spp. 1360 18.5 84.1 1047.11 13.8 78.2 1912.1 18.6 96.3 2053.7 10.2 90.4 1ydropsyche spp. 420.8 5.7 47 362 4.8 42.7 967.7 9.4 62 888.7 4.t4 55.9 Siniuliidae 525.8 7.2 77.7 415.6 5.5 73.8 390 3.8 69.4 640.7 3.2 75.5 Chironoaiidae 3195.2 43.5 93.9 4148.7 54.7 99.7 3289.7 32 100 5505 27.4 9E.9 Sabaeri app. 13 (a) 22 4.5 (a) 15.6 647.9 6.3 35.2 3973.6 19.8 51.3 All others 562.6 7.7 88.1 482.2 6.4 96.0 811.5 7.9 94 1393.2 6.9 95.8 Total Number 7337.8 7587.4 10285.9 20087.4 Total Taxa 89 85 83 98 CI) Comprisinq 2% or greater of the total number collected.
(2) Less than 2%.
LGS EROL TABLE 2.2-47 MEAN DENSITY (MG/Mz), PERCENT COMPOSITION (%), AND FREQUENCY OF OCCURRENCE (FO %) OF BENTHIC MACROINVERTEBRATES(*)
COLLECTED IN QUANTITATIVE SAMPLES FROM THE RIFFLE BIOTOPE OF EAST BRANCH PERKIOMEN CREEK, ALL STATIONS COMBINED 1973 1974 Taxon % FO % Mq/M 2 % IFO %
Dugesia spp. 20.9 (2) 31.5 169.1 5.2 51.9 Oligochaeta 59.8 3.1 62.3 67.3 2.1 63.9 Cambarus bartonia 236.5 12.3 6.2 207.6 6.3 6.5 Orconectes limosus 178.1 9.2 0.9 240.3 7.3 3.2 Stenelmis spp. 69.2 3.6 72. 9 170.4 5.2 88.9 Chimarra spp. 158.6 8.2 50.2 320.6 9.8 71.3 Cheumatopsyche spp. 384.4 20 78.2 678.7 20.7 96.3 Hydropsyche spp. 373.1 19.4 42.7 721.1 22 62 Simuliidae 36.8 2.9 73.8 36.6 (2) 69.4 Chironomidae 216.3 11.2 99.7 262.5 8 100 Sphaerium spp. 3 (2) 15.6 146.1 4.5 35.2 All Others 168.9 8.8 89.4 258 7.9 95.4 Total 1925.6 3278.3 (1) Comprising 2% or greater of the total dry weight biomass in 1973 or 1974.
(2) Less than 2%.
(Note: mean total biomass in 1976 was 5790)
LGS EROL TABLE 2.2-48 MONTHLY DENSITIES (MEANNO./M 2 ) OF IMPORTANT AND TOTAL TAXA OF BENTHIC MACROINVERTEBRATES COLLECTED FROM EAST BRANCH PERKIOMEN CREEK, AND PERKIOMEN CREEK, ALL STATIONS ANDYEARS COMBINED 1972-1976 Jan Feb Mar Apr May June Jul Aug Sep Oct Nov Dec Taxon No./M2 No.IM2 No./14 No./M9 No./MN No.IM No./M 2 No./M No./M No.1M9 No-IM2 N°'1M2 Dugesla spp. 30.1 47.3 33.4 42.1 46.2 140.3 196.9 578.5 926.9 771.9 679.1 296.0 UTT9oiaeta 37.2 114.3 81.7 156.5 234.3 168.7 61.8 67.0 112.5 84.8 185.9 66.1 Erpodbdel a r *t 1.2 1.9 1.1 1.6 1.9 13.8 4.9 3.6 4.5 3.9 3.4 2.6 ia bartonius rco~e~ 0.2 0.2 0.2 0.8 0.9 1.1 1.0 0.4 0.8 0.4 0.2 0.1 0.3 0.1 -0.4 0.4 0.4 0.7 0.5 0.2 0.2 0.2 Caenis sp. (n--*Ws) 17.2 16.0 17.3 46.6 53.2 9.0 51.3 16.4 263.3 118.1 102.7 48.5 Tricorithodes sp. (nymphs) 1.3 0.3 10.4 7.7 24.4 123.9 28.1 - -
aspp. (nymphs) 7.8 37.1 21.7 71.4 414.3 26.2 205.8 177.6 311.3 502.0 411.7 246.2 Batspp. (nymphs) 1.4 5.4 6.8 14.5 476.5 488.5 711.4 1059.3 1184.5 146.7 6.2 0.5 Stenonema spp. (nymphs) 19.7 41.0 28.5 59.6 72.5 44.4 98.3 89.9 285.2 313.5 245.1 84.9 Xt3'j7sp. (nymphs) 7.1 5.5 5.0 4.9 4.8 4.1 1.8 12.6 43.1 42.8 25.9 19.8 AloapnIa spp. (nymphs) 119.7 78.4 20.2 0.5 0.1 0.7 - 0.1 0.2 4.1 164.8 205.3 S ida (nymphs) - - 63.3 130.5 13.1 - - -
(aduts) ai-d-e - 0.1 - - 3.2 2.5 10.0 11.1 0.6 25.9 1.3 Corixidae (nymphs) - - - 4.7 28.8 6.0 7.9 1.9 0.2 -
Corydalus cornutus (larvae) 0.8 1.6 1.1 0.8 0.7 0.4 0.5 1.3 1.5 0.9 1.0 0.7 Pse1henus herricki (adults) - 0.5 0.2 0.9 0.1 1495 620 118.3 n herricki (larvae) 6.3 18.9 35.6 26.2 20.9 21.0 12.6 31.0 31.5 149.5 62.0 18.3
_____ _ spp a ults) 6.9 24.6 27.4 52.0 82.8 127.3 117.4 147.1 182.5 171.1 158.0 78.0 Stenelmis spp. (larvae) 15.7 41.8 132.1 429.8 485.6 840.1 670.4 1068.7 1612.8 921.2 458.5 254.0 hi'marra spp. (larvae) 25.5 271.0 145.2 174.0 48.8 395.0 754.5 2024.8 2784.3 1804.9 1103.9 471.3 Chimarra spp. (pupae) - - - 0.3 9.3 0.5 53.3 59.4 331.5 0.1 0.1 psyche spp. (larvae) 243.3 502.1 304.1 262.6 390.2 1659.7 2687.2 2597.0 3740.7 2795.8 2424.0 1054.6-25.6 8.2 21.2 11.5 19.1 15.3 0.4 -
spp. (pupae) - - -
Hdropsychespp.spp. (larvae) .75.0 142.1 95.5 120.1 559.7 724.2 1145.0 1118.4 1389.7 1324.4 1072.4 257.7 (pupae) - - 17.8 8.0 52.4 9.7 21.2 9.9 0.3 Leucotrichia pictipes (larvae) 17.8 21.0 22.0 21.5 0.6 30.6 96.9 161.8 348.0 187.6 138.1 55.3 Lectrct pitepes (pup.6 (pupae) 2.1 2.2 2.7 0.6ctriciai 0.1 0.2 3.5 3.5 0.2 - -
T-- 1.5 1.7 1.0 0.5 0.1 0.7 0.2 1.1 0.6 5imuliTdae (larvae) 240.6 358.2 195.9 104.7 1242.7 877.4 783.7 752.1 988.8 314.3 1388.2 515.6 2.4 0.2 2.1 11.2 15.6 153.0 177.6 50.5 50.3 36.6 11.8 4.0 Simullidae (pupae)
Chironomidae (larvae) 1854.5 3654.5 4184.0 4850.0 6783.0 3331.2 3734.4 3090.5 6314.7 3052.2 2902.2 1783.1 Chlronomldae (pupae) 15.4 88.2 315.4 313.3 708.1 285.6 262.3 185.4 196.7 141.0 86.5 73.0 10.9 12.7 9.2 3.1 7.1 44.1 69.2 140.9 367.1 226.3 109.9 64.4 Physa acuta 624.2 p spp. 8.0 16.8 11.7 6.9 8.6 64.0 120.9 1127.9 2807.6 2979.9 1175.4 All Others 85.7 149.6 175.2 283.3 207.3 228.9 266.9 397.2 912.0 519.5 459.5 230.8 2849.8 5655.4 5882.2 7170.1 12163.9 19810.6 12227.1 15047.4 25042.5 16649.2 13372.5 6556.6 Total Number 3.5 2.7 Total Biomass (G Day Weight) 1.0 1.8 1.5 1.4 1.9 2.4 2.4 2.9 4.2 4.5
0 0 LGS EROL Page 1 of 8 TABLE 2.2-49 SPATIAL DISTRIBUTION, BYSTATION BY YEAR, OF IMPORTANT BENTHIC MACROINVERTEBRATES COLLECTED IN QUANTITATIVE SAMPLES (1972-1976) FROM THE RIFFLE BIOTOPE OF EAST BRANCH PERKIOMEN CREEK AND PERKIOMEN CREEK E1eph*, Branch Sellersv lle Cathill No./mbX) %(2) FO %(3) No./m 2 % FO % No./mý % FO % No./m 2 % FO %
Dga spp.
(4) (4) 3.3 186.6 2.8 60 13.4 (4) 33.3 (4) (4) 2.2 1973 3.3 (4) 13.7 43 (4) 37 1.4 (4) 11.1 1974 13.9 (4) 50 15 (4) 33.3 56.7 (4) 41.7 1976 7.1 (4) 26.8 130.7 (4) 68.2 417 3.3 84.1 2.3 (4) 13.6 Mean 5.2 102.1 109.6 (4) 01igochaeta 1972 15.6 31.7 58.4 (4) 73.3 403.4 6.8 85 43 (4) 62.2 1973 58.8 68.6 76.9 (4) 57.4 515.9 8.6 83.3 59.7 2.2 66.7 1974 128.9 2.1 72.2 112.8 (4) 52.8 597.2 6.9 83.3 33.6 (4) 47.2 1976 95.4 (2) 63.4 50.9 (4) 54.5 671.4 5.4 90.9 142.7 (4) 72.7 Mean 66.4 71.9 531.5 70.7 Erpobdella punctata (4) (4) 5.0 2.3 (4) 15 5.6 (4) 26.7 1973 (4) (4) 5.9 (4) (4) 3.7 10.8 (4) 33.3 1974 3.9 (4) 30.6 2.2 (4) 11.1 11.4 (4) 52.8 1976 1.4 (4) 9.1 46.1 (4) 70.5 2.7 13.6 Mean 1.1 1.6 (4) 17.3 (4) (4) (4)
Cambarus bartoni 1.1 (4) 10 (4) (4) 3.3 (4) (4) 1.7 1973 5.1 (4) 31.4 (4) (4) 3.7 (4) (4) 3.7 1974 6.9 (4) 36.1 (4) (4) 2.8 1976 2 (4) 14.6 1.4 (4) 13.6 (4) (4) 2.3 Mean 3.5 (4) (4) (4)
Orconectes limosus (4) (4) 3.3 (4) (4) 6.7 (4) (4) 1.7 1973 (4) (4) 2 (4) (4) 1.9 1974 (4) (4) 5.6 (4) (4) 2.8 1976 (4) (4) 2.3 (4) (4) 6.8 Mean (4) (4) (4)
Caenis spp. 6.7 M-2 56.3 (4) 26.7 300.2 4.5 81.7 62.5 (4) 66.7 (4) (4) 58.8 388.1 3.4 79.6 33.5 (4) 61.1 1973 44.6 (4) 2.8 49.4 (4) 83.8 465.3 6.3 75 81.9 77.8 (4) (4) 1974 4.5 1976 33.4 (4) 51.2 214.3 2.7 75 140.7 84.1 (4) (4) 46.8 335.8 75.8 (4)
Mean (4)
Tricorthodes spp 19/Z (4)
(4) 1.9) (4) 1.9 1973 1974 (4) (4) 2.8 1976 Mean (4) (4)
LGS EROL Page 2 of 8 TABLE 2.2-49 (Cont'd)
El eph~,fl Branch Sellersville Cathill No./m l') %(2) FO %(3) No./m 2 % FO % No./m 2 % FO % No./m % FO %
Ephemerella spp.
1972- - -.. (4) (4) 1.7 -
1973 (4) (4) 3.9 - - (4) (4) 1.9 - -
1974 1.4 (4) 2.8 ..- -.
1976 - - - (4) (4) 2.3 -
Mean (4) - - - (4) - -
Baetis spp.
- 972 75.8 (4) 30 628.3 9.5 50 36 (4) 45 1.4 (4) 11.1 1973 58.2 (4) 33.3 510.2 4.5 59.3 46.8 (4) 50 (4) (4) 3.7 1974 10.8 (4) 30.6 483.6 6.5 75 243.3 2.8 86.1 2.2 (4) 16.7 1976 40.7 (4) 41.5 447.3 5.6 54.5 49.1 (4) 45.5 8.2 (4) 18.2 Mean 50.9
- 527.5 80.5 2.9 Stenonema spp.
7 (4) 8.3 12.5 (4) 31.7 6.1 (4) 30 - - -
1973 14.4 (4) 35.3 26.9 (4) 44.4 5.8 (4) 24.1 - -
1974 72.8 (4) 91.7 3.3 (4) 22.2 18.9 (4) 47.2 - - -
1976 82 (4) 53.7 10.5 (4) 29.5 5.1 (4) (4) (4) (4) 2.3 Mean 37.9 14.4 8.1 8.1 (4)
" 7 (4) (4) 1.7 37.6 (4) 33.3 7 (4) 28.3 (4) (4) 2.2 1973 (4) (4) 7.8 42.2 (4) 51.9 7.6 (4) 35.2 (4) (4) 7.4 1974 (4) (4) 5.6 9.2 (4) 30.6 20.6 (4) 55.6 2.2 (4) 8.3 1976 (4) (4) 2.4 10 (4) 56.8 15.7 (4) 56.8 6.8 (4) 38.6 Mean(4) 27.4 11.6 2.4 Allocapnia spp. 335.7 41.7 3 (4) 15 - - (4) (4) 2.2 fur- 7.1 -
1973 173.7 3 45.1 12.7 (4) 31.5 2.8 (4) 18.5 - - -
1974 510.3 8.4 38.9 6.7 (4) 22.2 5.6 (4) 22.2 - - -
1976 144.4 2.3 31.7 12.5 (4) 22.7 5.7 (4) 18.2 (4) (4) 2.3 Mean 283.5 8.6 (4) 3.1 (4)
Perlesta placida 1972 115.4 2.4 16.7 9.3 (4) 8.3 1.1 (4) 6.7 - - -
1973 147.4 2.6 29.4 22.1 (4) 24.1 6 (4) 16.7 (4) (4) 1.9 125.8 2.1 30.6 26.4 (4) 22.2 3.3 (4) 13.9 - - -
1974 1976 12.4 (4) 7.3 27.5 (4) 11.4 4.5 (4) 9.1 -- -
Mean 103.6 20.2 3.6 (4)
Coriyidae (4) (4) 5 - - - - - - -
1972 1973 43.4 (4.) 33.3 1.8 (4) 3.7 (4) (4) 1.9 - - -
161.4 2.7 52.8 (4) (4) 2.8 - - -.
1974 1976 142.4 2.2 41.5 (4) (4) 4.5 1.4 (4) 2.3 Mean 74 (4) (4)
LGS EROL Page 3 of 8 TABLE 2.2-49 (Cont'd)
El ephy~ %2 Brancý Sel IersvP Ie Cah I Cordalus cornutus 1972 1973 1974 (4) (4) 5.6 1976 Mean (4)
Psephenus hericki 1972 3.9 20 (4) (4) 2.2 (4) 1973 (4) (4) 7.8 9.4 (4) 33.3 (4) (4) 3.7 (4) (4) 1.9 1974 1.4 11.1 18.9 41.7 1.7 16.7 (4) 2.8 1976 2.4 (4)4 22 65.9 68.2 23 36.4 1.1 9.1 Mean (4) 22.3 5.6 (4)
Stenelmis spp.
1972 107 2.3 70 174.9 2.7 71.7 82.1 (4) 61.7 29.9 (4) 55.6 1973 81.2 (4) 86.3 186 . 2 (4) 74.1 69.1 (4) 70.4 13.9 (4) 46.3 1974 149.2 2.5 86.1 112.8 (4) 86.1 349.7 4 94.4 21.9 69.4 1976 140.2 2.2 82.9 363.2 4.6 79.5 1360.5 10.9 97.7 58.6 97.7 Mean 115.3 209.2 418.1 30.5 Chimarra spp.
(4) (4) 3.3 283 4.3 60 40.1 (4) 48.3 6.2 (4) 24.4 1973 12.2 (4) 19.6 397.1 3.5 55.6 58.5 (4) 40.7 (4) (4) 7.4 1974 9.4 36.1 747 . 5 10 83.3 276.1 3.2 83..3 5.6 27.8 1976 35.1 31.7 671 .1 8.5 86.4 54.5 (4) 72.7 3.6 15.9 Mean 13.1 489 92.3 3.8 Cheumatopsyche spp. 23.8 19/Z 1123.1 66.7 592.3 9 93.3 731.7 12.3 85 1408.6 21.7 80 2.8 1973 162 62.7 1052 9.3 68.5 476.7 8 79.6 183.6 6.7 72.2 1974 662.8 10.9 88.9 1732.8 23.3 91.7 1763.9 20.3 100 1312.2 24.7 97.2 1976 187.8 2.9 58.5 1753 22. 1 90.9 969.3 7.8 97.7 553.4 4.7 93.2 Mean 570.3 1195.1 906.2 809.4 Hydropsyche spp.
25.8 (4) 31.7 136.2 2.1 55 (4) (4) 8.3 (4) (4) 2.2 1973 (4) (4) 5.9 156.1 (4) 55.6 5.2 (4) 18.5 (4) (4) 1.9 1974 4.4 13.9 624.2 8.4 83.3 10.8 61.1 4.4 (4) 13.9 1976 4)
((4) 4.9 581.8 7.3 77.3 3.9 22.7 7.5 (4) 27.3 (4) 9.4 Mean (4) 333.4 4.6 2.9 Leucotrichia pictipes (4 1.7 (4) 1973 (4) (4) 1.9 (4) 1974 1.1 8.3 (4) (4) 8.3 1976 (4) (4) 4.5 2 (4) 9.1 Mean (4) (4) (4)
0 LGS EROL Page 4 of 8 TABLE 2.2-49 (Cont'd)
Eieph(9) Branch Sellersvlle Cathil1 No.ImP'*) %(2) FO %(3) No./m 2 % FO % No./m % FO % No./ml % FO %
T!-p2spp.
1.8 (4) 8.3 3.2 (4) 15 (4) (4) 3.3 1973 5.1 (4) 29.4 1.4 (4) 9.3 (4) (4) 1.9 1974 3.3 27.8 (4) 2.8 5.6 1976 11.2 36.6 3.2 (4) 22.7 (4) 4.5 (4) 4.5 Mean 5 2.1 (4)
Simulidae 1972 574.4 12.2 55 564 8.5 80 252.7 4.2 85 1365.6 21 88.9 1973 170.6 3 58.8 713.1 6.3 79.6 584.8 9.8 85.2 192.8 7 55.6 1974 173.9 2.9 44.4 476.4 6.4 86.1 941.7 10.9 75 269.2 5.1 83.3 1976 136.6 2.1 36.6 770.9 9.7 77.3 246.6 (4) 81.8 1988 16.9 93.2 Mean 292.7 636.2 471.6 944.2 Chironomldae 1972 2192.8 46.5 75 3302 50 100 3831 64.3 100 3572 55 100 1973 4488 77.8 100 7516.1 66.1 100 4006 66.9 100 2289.9 83.2 100 1974 3706.9 61.1 100 2486.4 33.4 100 3790.3 43.7 100 3640 68.6 100 1976 5007.3 78.4 90.2 2565.9 32.3 90.9 4126.8 33 100 7678.2 65.3 100 Mean 3719.2 4156.7 3939.2 4208.3 Physa acuta 8.8 (4) 28.3 5.2 (4) 25 261.1 4.4 46.7 20.8 (4) 20 1973 29.5 (4) 35.3 5.4 (4) 13 31.3 (4) 53.7 2.2 (4) 9.3 1974 8.9 (4) 38.9 9.2 (4) 47.2 80.3 (4) 72.2 4.2 (4) 16.7 1976 42.7 (4) 39 9.1 (4) 29.5 10 7.3 77.3 1156.4 9.8 65.9 Mean 21.8 6.9 10.7 291 Sphaerium spp.
1972 5.6 (4) 23.3 5.6 (4) 25 11.1 (4) 21.7 1973 2.1 (4) 17.6 3 (4) 20.4 2.8 (4) 20.4 1974 10.3 (4) 27.8 1.1 (4) 8.3 96.4 (4) 69.4 1976 5.9 (4) 22 8.9 (4) 34.1 2659.8 21.3 90.9 (4) (4) 4.5 Mean 5.6 4.8 625.3 (4)
All Others (4) 62.2 1972 67.4 (4) 61.7 289.8 4.4 95 211.8 3.6 90 49.7 268.7 4.7 98 206.3 (4) 96.3 118.9 (4) 90.7 6.8 (4) 33.3 1973 4.1 100 110.3 (4) 88.9 16.9 3.7 97.2 11.1 (4) 44.4 1974 249.2 260.7 4.1 87.8 240.9 3 90.9 780.2 6.1 100 139.3 (4) 77.3 1976 Mean 199 222.1 334.4 51
0 LGS EROL Page 5 of 8 TABLE 2.2-49 (Cont'd)
Moyer Wawa Spring Punt Rahms No.m 2 % FO % No./m 2 % FO % No./lm % FO % No./m 2 FO %
Do esla spp.
191.6 2.5 60 178.9 (4) 61.7 89.2 (4) 71.7 163.9 (4) 54 1973 107.3 (4) 51.9 82.2 (4) 74.1 225.8 (4) 53.7 75.8 (4) 46.3 1974 781.7 5.6 86.1 1407.8 6.9 100 186.4 (4) 69.4 166.9 (4) 80.6 1976 3229.1 10.6 93.2 2938.4 5.8 90.9 731.1 3.4 77.3 190.5 (4) 79.5 Mean 966.5 1005.9 290.9 144.8 Oigochaeta 1972 29.9 (4) 53.3 61.1 (4) 50 36.9 (4) 63.3 101.7 (4) 64 1973 21.7 (4) 46.3 38.8 (4) 51.9 39.4 (4) 63 55.2 (4) 61.1 1974 46.1 77.8 41.1 (4) 50 88.9 (4) 80.6 136.9 (4) 77.8 1976 18.6 (4)
- 4) 63.6 39.3 (4) 38.6 26.6 (4) 54.5 81.8 (4) 79.5 Mean 28.1 46.3 44.9 90.2 Erpobdella punctata 1.4 (4) 11.7 4.1 (4) 21.7 1.8 (4) 10 (4) (4) 2 1973 (4) (4) 3.7 2.8 (4) 16.7 (4) (4) 5.6 3.2 (4) 24.1 1974 2.5 (4) 19.4 8.1 (4) 41.7 (4) (4) 2.8 1.8 (4) 13.9 1976 4.5 (4) 22.7 9.3 (4) 31.8 (4) (4) 2.3 1.8 (4) 15.9 Mean 2 5.7 (4) 1.9 Cambarus bartont 1972 1973 1974 1976 (4) (4) 6.8 Mean (4)
Orconectes limosus (4) (4) 6.7 (4) (4) 3.3 (4) (4) 3.3 (4) (4) 2 1973 (4) (4) 1.9 (4) (4) 3.7 1974 1.1 (4) 11.1 (4) (4) 2.8 (4) (4) 2.8 1976 (4) (4) 4.5 (4) (4) 2.3 Mean (4) (4) (4) (4)
Caenis M2spspp.
1.3 (4) 10 24.7 (4) 51.7 4.1 (4) 13.3 11.4 (3) 30 1973 (4) (4) 7.4 3.2 (4) 20.4 8.4 (1) 25.9 64.7 (4) 55.6 1974 2.2 (4) 13.9 12.2 (4) 22.2 1.1 (4) 2.8 27.5 (4) 38.9 1976 54.5 (4) 52.3 12.7 (4) 38.6 - 26.4 (2) 43.2 Mean 13.4 13.7 3.8 33.8 Trico!thodes spp.
1972 (4) 1.7 15.2 (4) 18.3 43.7 (4) 20 324.3 2.7 44 (4) 1973 (4) (4) 5.6 4.2 (4) 11.1 11.4 (4) 16.7 1974 (4) (4) 5.6 15 (4) 30.6 10.8 (4) 36.1 1976 (4) (4) 2.3 22.5 (4) 15.9 18.4 (4) 25 65.7 (4) 34.1 Mean 10.1 21.6 109.3 Ephemerella spp.
1972 140.1 (4) 60 649.7 5.4 54 1973 (4) (4) 1.9 1.4 (4) 7.4 929.9 6.5 90.7 520.3 4.9 85.2 1974 (4) (4) 2.8 (4) (4) 2.8 1541.4 9.6 100 449.2 3.9 91.7 1976 (4) (4) 4.5 12.3 (4) 22.7 2631.6 12.3 86.4 511.8 2.9 79.5 Mean (4) 3.2 1185.1 539.5
LGS EROL Page 6 of 8 TABLE 2.2-49 (Cont'd)
Moyer Wawa Spring M unt Rahms No.lm2 % FO % No./m 2 % FO % No./m % FO % No./m 2 % FO %
Baetis spp.
2W2 51.5 30 249.3 (4) 46.7 361.5 4.4 45 759.4 6.3 58 1973 97.4 (4) 27.8 463.2 4.0 48.1 665.7 4.7 57.4 784.9 7.4 61.1 1974 106.4 (4) 58.3 387.2 (4) 61.1 823.9 5.1 83.3 716.9 6.3 72.2 1976 531.6 (4) 52.3 642.7 (4) 54.5 1345.5 6.3 63.6 1388 7.9 59.1 Mean 183.2 423.6 755.1 908.9 Stenonema spp.
f977- (4) (4) 3.3 366.5 4.4 83.3 371.8 3.1 66 1973 (4) (4) 5.6 6.8 (4) 18.5 656.1 4.6 100 460.4 4.3 85.2 1974 (4) (4) 2.8 675.8 4.2 100 229.2 2 94.4 1976 26.6 (4) 40.9 3 (4) 18.2 505 2.4 97.7 355.2 2 97.7 Mean 6.2 2.7 535.9 365.9 18.5 (4) 31.7 (4) 5 32 (4) 28 1973 8 (4) 24.1 9.2 (4) 33.3 11 (4) 31.5 20.9 (4) 37 1974 66.1 (4) 66.7 23.1 (4) 61.1 28.9 (4) 58.3 10.8 (4) 36.1 1976 47.7 (4) 95.5 18.2 (4) 61.4 21.1 40.9 29.1 (4) 36.4 Mean 25.3 16.7 13.5 23.9 Allocapnia spp. (4) 197Z (4) (4) 1.7 (4) (4) 1.7 41 (4) 26.7 14 (4) 22 1973 (4) (4) 1.9 17.3 (4) 16.7 43.6 (4) 40.7 1974 (4) (4) 2.8 (4) (4) 2.8 20.6 (4) 19.4 58.6 (4) 33.3 1976 (4) 2.3 8.9 18.2 83.6 (4) 25 Mean (4) 23.3 48.1 Perlesta placida 8.3 197Z 8.1 (4) 1.3 (4) 6 1973 J4) 6.2 (4) 14.8 10.2 (4) 11. 1 1974 (4) 2.8 33.1 (4) 30.6 11.1 (4) 22.2 1976 (4) (4) 4.5 (4) 2.8 33.1 30.6 1.8 (4) 9.1 Mean (4) 23.4 5.9 Corixidae 1972 (4) 1973 (4) 1.9 1974 1976 (4) 2.3 (4)
Mean Cordalus cornutus 1972 (4) (4) 1.7 (4) (4) (4) 6.7 (4) (4) 4 1973 (4) (4) 7.4 (4) 3.7 2.6 (4) 16.7 2.4 (4) 14.8 1974 (4) (4) 8.3 2.3 4.2 (4) 25 1.4 (4) 5.6 1976 3.9 (4) 27.3 (4) (4) 15.9 5.7 (4) 38.6 5. (4) 40.9 Mean 1.3. 3 2.3
LGS EROL Page 7 of 8 TABLE 2.2-49 (Cont'd)
Moyer 2 Wawa Spring Munt Rahms 2 No./m % FO % No./m 2 % FO % No./m % FO % No./m % FO %
Psephaenus herricki 1972 19.2 (4) 33.3 18.5 (4) 63.3 3.6 (4) 20 24.5 (4) 60 1973 10.2 (4) 37 47.6 (4) 81.5 8.8 (4) 40.7 101.6 (4) 83.3 1974 69.4 (4) 50 117.2 (4) 83.3 11.7 (4) 55.6 112.5 (4) 86.1 1976 96.8 (4) 86.4 263 (4) 100 22.7 (4) 52.3 549.1 3.1 93.2 Mean 43.6 100.3 10.9 189.8 Steneimis spp.
1972 504.7 6.7 73.3 731.5 5.9 85 24.2 (4) 65 404.9 3.4 98 1973 370 4.7 77.8 1178.4 10.1 83.3 38.8 (4) 77.8 632.8 6 90.7 1974 715.8 5.2 97.2 2711.7 13.3 100 100.6 (4) 97.2 636.4 5.6 94.4 1976 4869.1 16 100 7296.6 14.4 100 382.5 (4) 95.5 783 4.4 100 Mean 1496.2 2712.4 123.7 607.5 Chimarra spp.
1972 975,4 12.9 60 2708.6 21.7 95 138 (4) 76.7 287.3 2.4 58 1973 485.1 6.2 79.6 2442.1 20.9 96.3 79.3 (4) 81.5 609.1 5.7 83.3 1974 1634.7 11.8 97.2 3359.2 16.5 100 73.6 (4) 80.6 440 3.8 88.9 1976 4720.5 15.5 100 5409.1 10.7 100 1427 6.7 93.2 2235.5 12.7 97.7 Mean 1810.7 3367.6 402.1 877.5 Cheumatopsyclhe spp.
1972 2360 31.3 90 1956.6 15.7 96.7 1255.2 15.2 96.7 2191.4 18.3 96 1973 2724.6 34.8 88.9 1636.2 14 96.3 1322.6 9.2 100 2007 18.9 100 1974 4478.9 32.3 100 1522.2 7.5 100 1837.8 11.5 100 2535.8 22.2 100 1976 5739.1 18.8 100 2992.5 5.9 100 2669.8 12.5 100 2557.7 14.5 100 Mean 3621.1 2021.8 1702.9 2292.3 Hydropsyche spp.
1972 1278.9 16.9 83.3 977.4 7.8 98.3 888.5 10.8 91.7 1067.1 8.9 90 1973 664.9 8.5 79.6 1325 11.3 92.6 922.5 6.5 100 1264 11.9 98.1 1974 2109.7 15.2 100 3052.8 15 100 659.2 4.1 100 952.8 8.3 100 1976 1771.4 5.8 100 2906.4 5.7 100 1102.5 5.2 97.7 1476.4 8.4 100 Mean 1373.8 1896.8 904 1200.4 Leucotrichia pictipes 1972 80.1 33.3 233 38.3 78.7 (4) 36.7 134.2 (4) 38 1973 27.9 35.2 35.8 31.5 26.9 (4) 48.1 27.1 (4) 33.3 1974 354.7 2.6 61.1 434.2 2.1 61.1 126.1 (4) 66.7 117.8 (4) 61.1 1976 476.1 (4) 88.6 942.3 (4) 84.1 130.7 (4) 63.6 116.6 (4) 45.5 Mean 206.3 376.3 84.9 95.3 Tipula spp. (4) 3.3 (4) 2 (4) (4) (4) 1.7 (4) (4) 1.7 (4) 1973 (4) (4) 3.7 (4) (4) 5.6 (4) (4) 7.4 1974 (4) (4) 5.6 1976 (4) (4) 6.8 (4) (4) 9.1 (4) (4) 6.8 Mean (4) (4) (4) (4)
0 LGS EROL Page 8 of 8 TABLE 2.2-49 (Cont'd)
Moyer Wawa Spring M unt Rahms 2 Nq./m 2 % FO % No./m 2 % FO % No./m % FO % No./m % FO %
Simuliidae 1972 358.4 4.8 83.3 249.5 (4) 85 1241 15 98.3 1287.7 10.7 78 1973 330.9 4.2 85.2 487.9 4.2 77.8 1135.4 7.9 94.4 782 7.4 96.3 1974 219.2 (4) 63.9 259.4 (4) 63.9 2131.9 13.3 100 1885.6 16.5 97.2 1976 319.5. (4) 81.8 348.4 (4) 79.5 1416.8 6.6 97.7 2048.9 11.6 97.7 Mean 316.6 340.1 1416.8 1438.3 Chi ronomi dae 1972 1516.2 20.1 100 4851.1 38.8 98.3 2900.9 35.1 96.7 3405.1 28.4 100 1973 2769.4 35.3 98.1 3841.7 32.8 100 7208.7 50.4 100 2552 24.1 100 1974 - 3004.7 21.7 100 3109.7 15.3 100 6548.1 40.9 100 2332.2 20.4 100 1976 7563.4 24.8 100 6054.3 12 100 7114.3 33.2 10 4483 . 4 25.5 100 Mean 3512.8 4519.9 5732.4 3202.7 Physa Acuta 1972 10 (4) 20 (4) (4) 6.7 78.9 (4) 58.3 8.6 (4) 24 1973 47.2 (4) 42.6 (4) (4) 3.7 44.2 (4) 50 7.4 (4) 35.2 1974 13.6 (4) 38.9 (4) (4) 2.8 83.9 (4) 72.2 3.9 (4) 27.8 1976 29.5 (4) 38.6 2.3 (4) 11.4 178 (4) 77.3 9.1 (4) 29.5 Mean 25.5 (4) 92.6 7.4 Sphaerium spp.
191Z 10.6 (4) 28.3 41.8 (4) 28.3 17 (4) 46.7 70.5 (4) 38 1973 4.8 (4) 5.6 13.9 (4) 29.6 12.1 (4) 40.7 12.7 25.9 1974 2.5 (4) 19.4 3776.9 18.6 86.1 8.1 (4) 33.3 108.3 (4) 66.7 1976 510.2 (4) 63.6 20385.9 40.3 90.9 175 (4) 72.7 93.2 65.9 Mean 120.8 5341.3 49.8 66.4 All Others 1972 154.7 2 75 176 (4) 75 540.1 6.5 100 668.4 5.6 98 1973 163.3 2.1 90.7 88.8 (4) 83.3 933.7 6.5 100 550.8 5.2 98.1 1974 261.3 (4) 88.9 130 (4) 94.4 1017.8 6.4 100 486.4 4.3 100 1976 430.7 (4) 100 263.4 (4) 97.7 1432.7 6.7 100 518.2 2.9 97.7 Mean 239.4 163 940.8 562.3
)Mean density.
,2,Percent composition.
3
( )Frequency of occurrence.
( 4 )Less than I/square meter or less than 2%. Erpobdella punctata, Cambarus bartoni, Orconectes limosus, Argia spp, Corydalus cornutus, and Tipula spp. were dominant only as biomass (see Table 2.2-50).
0 LGS IPOL TABLE 2-2-50 (Paqe 1 of 6)
SPATIAL DISTRIBUTION, BY STATION BY YEAR, CF IMPORTANT BENTHIC MACROINVERTEERATES COLLECTED IN QUANTITATIVE SAMPLES (1973, 1974) FROM THE RIFFLE BIOTCPE OF EAST BRANCB PEIRKICMEN CREEK AND PERKIOMEN CREEK Elephant Branch Sellers'vill~e Cathill ma/0" Iý2) hM!/M .4.. eM/Rn 1973 (a) C3) 15.3 (3) (3) (3) 1974 5.6 C3) 4.4 (3) 23.5 (3)
Mean 2.9 10.9 9.5 Oliqocbaeta 1973 56.7 2.3 54.7 3.6 115.3 7.0 9.8 3.2 1974 33.3 (3) 54.7 2.4 84.6 3.8 15.2 (3)
Mean 4117.0 54.7 103.0 12.0 IZzodella uRnita 1973 12.7 C3) 1.7 (3) 43.6 2.6 1974 14. 9 C3) 2.4 (C) 117.6 5.3 Mean 13.6 2.0 73.2 Cambagg bAt 1973 891.4 35.7 202.6 13.5 361.5 21.9 1974 797.0 341.5 448.5 20.2 Mean 852. 3 121.6 396.3 orcoectsl1mosus 1973 554.2 22.2 4811.9 29.,,4 1974 72.7 3.1 314.4 14.2 Mean 354.6 416.7 CLtnim 8pp.
1973 4.1 C3) 11.4 C3) 2.9 C3)
Cu) 1974 7.9 (3) 21.4 (C) 8.3 Cu)
(u)
Mean 5.7 15.4 5.1 Trcoythde app.
1973 C3) (3) (3) 1974 (3) (3)
Mean (3) g~biexe 1lla sipp. Cu) 1973 (3) (3)
C3) 1974 (3)
(I) Cu)
Mean Baeti1s app. (3) 1973 5.4 (3) 34. 1 2.3 2.7 (3) (3)
Cu) (3) (3) 1974 1.6 34.0 (3) 12.1 Mean 3.8 34.1 6.5 ca)
StenngDm.@ spp. Cu)
(3) 1973 4.8 12.5 (3) 1.5 Cu)
CS) 1974 48.9 2.1 c3) (C) 4.4 Mean 23.0 1.7 2.7 Cu)
Aa~si spp.
1973 cu) (3) 70.0 4.7 10.4 (3) (3) 1974 1.9 C3) 9.6 (3) 25.0 (3) C3)
Me an (3) 45.8 16.2 (3)
LGS EROL TABLE 2-2-50 (Cont'd) (Paqe 2 cf 6)
Elephant Erancb Sellersville Catbill, Lmg/L Nq/tn' Alloggngauil s vip.
1973 22.8 (2) 1. 5 (2) (3) (3)
(3) (3) (3) 1974 77.6 3.4 (2)
Mean 45.5 1. 1 1973 43.5 (3) 7.6 (3) 3.8 (3) (3) (2) 1974 31.6 (3) 33.7 (2) 1.1 (3)
(2)
Mean 38.5 18.0 2.7 Corixidae (2) 1973 39.0 (C3) (2) (3) (3) 1974 99.6 4.3 (3) (3)
Mean 64.1 (3) (3) 1973 1974 1.2 Mean (3) 1973 (3) (2) 8.4 (a) (3) (3) (3) 1974 1.8 (3) 7.7 (X) 1.5 (32) (3) (3)
Mean CI) 8.1 (,) (3) 1973 24.5 (3) 55.1 3.7 18.3 5.7 (3)
(2) C3) (3) 1974 42.2 32.1 65.1 2.9 7.5 Mean 31.8 45.9 37.0 6.4 Ch.maxrr spp.
1973 (3) C() 83.0 5.5 13.2 (3) (3) (2) 1974 1.9 (3) 320.1 14.3 88.7 4.0 (3) (3)
Me an 1. 1 177.8 43.14 (3)
Cheumptoysyche spp.
1973 97.9 3.9 419.7 27.9 197.1 11.9 107.9 34.8 1974 359.2 15.5 813.8 36.2 561.0 25.3 689.1 70.4 Mean 206.0 577.4 342.7 340.4 Hydropsyche sppi. (2) (2) 1973 (3) (2) 188.1 12.5 7.3 (3)
(2) (2) 5.6 (3) 1974 (3) 477.8 21.3 18.3 Mean (3) 304.0 11.7 2.2
rGS Z*fO TABLE 2-2-50 (Cont'd) (Paqe 3 cf 6)
Elej~bant Prancb Sellersville Catbill 2 Naft ICR g/SJI % ~maimm Leucotricbia Di&ti]*e 1973 (2) (3) Ca)
(a) C3) Ca) 1974 9.)
Ca)
Mean 8.1 2.6 1973 99.3 4.0 43.41 2.9 1.6 Cap 11.1 (C) 1974 117.7 5.1 (a) 9.3 Mean 106.9 26.0 1973 15.5 £43) 70.8 4.7 76.4 4.6 40.6 13.1 (3) 71.4 3.2 .52.3 2.4 35.1 3.6 1974 19.2 Mean 17.0 71.1 66.8 38.41 Ckiironomidae 216.3 13.1 133.0 42.9 1973 457.4 18.3 178.8 11.9 21.0 305.8 13.6 205.4 9.3 205.9 21.0 1974 484.8 468.7 229.6 212.0 162.2 Mean Pwx aSlit (a) 45.6 2.8 3.5 (3) 1973 110.8 4.14 5.1 Ca) 1971 13.3 (1) 9.5 (a) 48.9 2.2 6.6 70.4 6.9 46.9 4.7 Mean anbasziia app. 1973 (3) (3) 4.3 C(a) (a) (2)
(a) C(a) 28.7 Ca) 1974 (a)
Mean 2.7 11.9 All Ctheru 418.0 2.9 (3) Ca) 1973 52.2 2.1 33.0 2.2 107.4 4.8 (3) Ca) 1974 80.1 3.5 45.9 2.0 71.8 cI)
Mean 63.8 38.1
IGS EROL TABLE 2-2-50 (Cont'd) (Paqe 4 of 6)
Mover Wawa Spring Mount Rabne
-- % mgqmm S Na/rn 1973 60.5 3.1 47.4 (3) 28.7 (3) 24.9 (3) 1974 362.6 6.3 618.8 10.1 31.0 (3) 38.0 (3)
Mean 181.3 275.9 29.6 30.1 Oliqoctbaeta 1973 106.0 5.4 16.0 (3) 100.0 2.4 87.6 2.2 1974 126.6 2.2 89.3 (3) 42.8 (3) 75.2 2.4 Mean 114.2 45.3 77.1 82.6 1973 3.8 (3) 41.0 (3) 13.5 (3) 38.3 (3) 1974 16.6 (3) 68.3 (3) (3) 47.8 (3)
Mean 8.9 51.9 8.1 42.1 1973 50.1 2.6 173.8 4.1 1974 1055.7 18.3 1.6 (3) (3) (3)
Mean 452.4 104.9 (3)
CAaeni app. (3) (3) C 3) 1973 C3) (3) (3) (3) 2.5 (3) 1974 (3) (3) (,) (3) (3) (3) (3)
(a)
Mean 1.9 Tricorvtbod epp. (3) 1973 (3) (3) (3)
(3) (3) 1.5 1974 (3) 1.5 (3) (3) (3)
Mean - (3) (3) 1.1 Eph-mrn.lUa spp. (3) 1973 (3) (3) (3) (3) 82.6 (3) 33.0 (3) 1974 (3) (3) (3) 264.1 7.5 33.7 (3)
Mean (3) (3) 155.2 33.3 DM.1tis spp. (3) 1973 5.0 c ) (a) (3) 15.9 C3) 36.7 52.7 1974 (3) (3) 8.0 (3) 28.9 65.7 57.2 Mean 6.2 21.1 48.3 54.5
+/-Stenonema spp. (3) 1973 (3) (3) (3) (3) 247.7 5.9 54.4 (3) 1974 (3) 213.1 6.1 55.9 (3)
(3)
Mean (3) 233.9 55.0 Araig spp.
1973 4.1 (3) 14.2 (3) 5.6 (3) 12.3 (3)
(3) 1974 65.7 46.7 (3) 34.7 (3) 11.3 (3)
Mean 28.7 27.2 17.3 11.9
GS EPOL TABLE 2-2-50 (Cont Id) (Paqe 5 of 6)
Moyer Wawa Sprinq Mount Rahns po/rn2 -J MQm -_ ma/mt L IL_
Allocauni apsp.
1973 (3) C3) (3) (3) 41. 1 (3)
(3) 1974 (3) (3) 2.2 (3) 3.9 (3)
Mean (3) 1.1 4.0 (3) (3) C3) 1973 (3) 3.k1 (3) 1974 21.9 (3) 1. 1 (3)
Mean (a) 10.0 2.0 Corixidae (3) 1973 (3) 19741 C(3)
Mean (3) 1973 2.2 17.11 615.3 14.6 112.0 3.5 (I) 1974 7.1 1100.1 11.1 129.6 1.2 Mean 4. 1 10.11 529.3 137.0
( 3)
(3)
(3) 1973 5.5 35.1 C(3) 8.6 (c) 30.5 (3)
(3) 85.3 1974 36.6 112.6 11.0 (3) 2.8 Mean 18.0 66.1 9.5 52.11
~SDS.en+/-el sp;p.
1973 75.3 3.9 233.7 6.3 12.1 (3) 113.2 2.8 1974 210.7 3.7 6611.7 10.8 41.2 (3) 184.3 6.0 Mean 129.5 106.1 23.9 111.7
.bimaaz Opp. (3) 187.7 4.6 1973 184.0 9.5 662.1 18.0 211.6 1974 659.7 11.5 852.5 13.8 23.5 (3) q147.2 4.8 Mean 374. 2 738.3 24.2 171.5 Cheuniatopsyche aPP.
1973 779.6 1o0.1 688.3 18.7 683.7 16.2 1116.9 28.3 1974 1328.5 23.1 320.6 5.2 539.2 15.11 800.3 26.0 Mean 999.2 541.2 626.0 1008.2 Hydrg.usyche app.
1973 106.8 20.9 1615.0 43.9 1058.0 25.1 1616.0 110.6 1974 1609.3 28.0 2215.1 36.0 872.4 24.9 831.2 27.0 Me an 887.8 1855.0 983.8 1320.1 1973 1.7 C.) 1.1 (3) 1.8 (3) (3) (3) 1971 18.9 (3) 25. 4 c() 1.5 (3) 7.4 (3)
Mean 8.6 11.0 2.9 3.3
LGS EROL TABLE 2-2-50 (Cont'd) (Page 6 of 61 Mover Wlawa Sprinq 2Mount 1Rah-ns
-s- i/rn M__
g/M % gm 1973 12.4 (3) 31.8 (3) (3) 52.0 1974 30.3 (3)
Mean 7.5 31.2 31.2 simul idae 1973 58.3 3.0 76.6 2.1 308.8 7.3 69.7 (:3) 1974 19.4 (3) 22.0 (3) 175.3 5.0 237.1 7.7 Mean 42.8 54*8 255.4 136.7 Cbironomidae 1973 131.1 6.7 194.7 5.3 491.4 11.7 185.3 4.6 1 974 160.3 2.8 212.6 3.5 436.5 12.4 162.7 5.3 Mean 142.8 201.9 469.4 176.2 Rhys acuta 1973 42.5 2.2 (3) C3) 24.6 (3) 8.9 (3) 1974 13.4 (3) 2.5 C 3) 41.9 (3) 2.3 Mean 30.9 1.0 31.5 6.3 (:3)
Sbkaerium spp.
(3) 1973 (3) 11.8 ( 3) 11.9 (3) 3.0 (:3)
(3) 1974 (3) 846.0 13.7 1.9 (3) 49.0 (3)
Mean 345.5 7.9 21.4 All Others 1973 14.9 (3) 10.3 (3) 246.5 5.9 156.0 3.8 1974 54.9 (3) 29.2 (3) 250.6 7.1 110.2 3.6 30.9 17.9 248.1 Me an 137.7 (1) Mean density in milliqrams of dry weiqbt Per square meter.
c 9) Percent of composition.
(3) Less than 1 Mcq square meter or less than 2%. Caenis spp., Tricorythodes spp., Perlesta placida, and Leucotrichia pictipes were dominant only numerically (see Table 2.2.-49).
LGS EPOL TABLE 2.2-51 (Paqe 1 of 2)
SUMMARY
TABLE OF AQUATIC MACROITNVEFTE!ATE DRIFT AS MEASURED FOR EACH MOWTHLY(C ) 211 HOUR STUDY IN EAST BRANCH PERFIOMEN CREEK AND PERKIOMEN CREEK. MONTHLY VALUES FOR INDIVIDUAL TAXA REPRESENT PERCENT CF TOTAL DRIFT Jjfl 1973 OnD MPI 121 "nS Oct I East Branch Perkiomen Creek Dominanta taxa
- spp. - Absent 9.4 9.8 4.6 43.8 7.1 2.2 9.0 Coenaqrionidae - Absent Absent (3) Absent Absent 2.7 Absent (3)
&nelmi spp. - 4.0 4.6 7.6 8.1 1.1 1.0 Absent 5.7 Chimarr spp. - 28.9 Absent (3) (a) Absent 3.0 Absent 4.3 Cheumatoosych spp. - .4.0 (a) 18.7 29.9 2.2 10.1 2.2 13.4 kvdropsvche spp. - 3.2 (3) q9.8 8.1 Absent 9.6 Absent 25.0 Chironomidae - 35.6 72.9 7.3 43.1 51.7 64.7 84.4 33.6 Total percent - 75.7 87.9 94.2 94.3 98.8 98.2 88.e 91.1 Total number/1000 m3 - 386 530 1921 902 689 1897 418 927 All taxa Total number
- SE/1000 m3 - 5100107 603*92 20390799 957*282 697t268 1932*485 471*164 1019*157 Total biomass (mq dry wt)
- SE/1000 m3 - 71*19 74115 352*148 192*50 57*38 223t107 80*30 148*28 Total taxa - 19 13 16 12 5 10 7 12 Velocity (mls) - 0.125 0.116 0.110 0.052 0.037 0.034 0.030 0.072 Perkiomen Creek Dominant' taxa Naididae - 0 0 0 0 0 0 0 Absent Gammarus fasciat - (j) Absent (3) (a) 1.4 C3) (3) (3)
Tricorvthodes op. - Absent Absent 6.7 3.4 1.0 (3) 1.0 3.4 Baetis spp. - Absent 17.5 7.0 (3) 33.2 18.1 3.1 -6.1 Cheumatonevc spp. - 5.3 (3) 13.9 4.5 12.2 3.6 (3) 6.4 Simuliidae - (3) 3.4 4.8 (3) (3) (S) 2.4 1.6 Chironomidae - 50.9 67.9 52.9 85.9 40.9 70.1 79.5 73.2 Beleidae - Absent Absent Absent (a) (a) (3) Absent (3)
Total percent - 56.4 88.8 85.3 95.8 93.8 89.7 87.0 S1.7 Total number/1000 m3 - 181 625 2358 10,126 1285 2807 592 2550 All taxa Total number
- SE/1000 m3 1991t539 321*60 704*204 2765*701 10570*2294 1433*485 2993*1107 680*140 2781M520 Total biomass (mq dry wt) t SE/1000 m 3 82*20 69t23 69*17 275*145 482*114 134015 201063 98*39 190*32 Total taxa 20 34 19 31 37 25 26 20 27 Velocity (mls) 0.146 0.360 0.238 0.244 0.171 0.101 0.116 0.110 0.191
0 LGS EROT.
TABLE 2.2-51 Cont'd) (Page 2 of 2) 1974 Apr Jun Jul sep Meaan East Branch Perkiomen Creek Dominant2 taxa Baelis spp. (3) 36.6 28.9 4.7 2.2 16.0 11.7 Coenagrionidae Absent Absent 1.3 (3) 7.1 3.0 (3)
Stenelmis spp. 5.7 2.5 1.3 30.0 (3) 3.0 7.1 Chimarra spp. 2.1 (3) (3) Absent Absent 1.0 (3)
Cheumatopspche spp. (3) Absent 4.4 3.2 3.5 6.0 2.9 s
11YqRpsychf pp. 2.0 26.9 9.1 1.1 2.2 7.0 8.1 Chironomidae 77.7 32.6 48.1 45.8 57.7 44.0 50.5 Total percent 88.5 99.1 93.6 85.3 73.2 80.0 86..
Total number/1000 m3 1077 1272 499 1267 806 450 1550.2 All taxa Total number t SE/1000 m3 3 1217+/-189 5320t2001 5 33+/-132 1485+/-551 11012+/-3697 562+/-91 3355+/-1110 Total biomass (mg dry wt) t SE/1000 M .130+55 34 8+/-187 22+/-5 384+/-345 453+/-156 42+/-10 229+/-126 Total taxa 19 20 16 17 28 19 20 Velocity (m/s) 0.116 0.090 0.150 0.037 0.034 0.049 0.079 Perkiomen Creek Dominant' taxa Naididae 2.9 48.3 (3) (3) (3) Absent 8.5 Gammarus fasciatus Absent Absent 1.4 (3) 9.4 2.2 2.2 Tricoathodes spp. Absent C3) 2.1 C3+/-
Absent (3) (3)
Baetis spp. 1.9 4.5 31.5 2.2 18.2 11.5 11.6 Cheumatopsyche spp. 1.4 (3) 7.8 1.5 41.1 8.4 10.0 Simuliidae 20.0 (3) 10.9 1.0 1.1 2.1 5.9 Chironomidae 56.7 43.6 31.9 78.4 13.3 50.5 45.7
£3) Absent 1.7 Heledae Absent (3) 10.4 (3)
Total percent 82.9 97.9 85.0 94.5 85.9 75.0 86.9 3
Total number/1000 M 610 9511 1047 10860 6312 2784 5187 All taxa Total number +/- SE/l000 m3 736+/-97 9715+/-807 1232t368 11492+/-4155 7348t2932 371 2+/-1036 5706+/-1565 Total biomass (rag dry wt) t SE/lO00 m3 43+/-15 251+/-46 86+/-29 629+/-244 488+/-171 152+/-50 27 4+/-925 Total taxa 30 23 28 47 41 35 34 Velocity (m/s) 0.322 0.138 0.247 0.131 0.137 0.170 0.191
(')Monthly values for individual taxa represent percent of total drift.
(2)Taxa which comprised t2% of the total number in either 1973 or 1974. Numerous other taxa were dominant in individual months.
C3)Drifting, but at levels below 21 of to+ýal.
LGE EROL TABLE 2.2-52 DIEL PERIODICITY OF AQUATIC DRIFT CN EAST BRANCH-PERFIOMEN CREEK AND PERKIOMEE CREEK EXPRESSED AS A PERCENT OF THE 24-HOUR TOTAL, ALL DRIFT STUDIES CCMEINED (
1000 1200 1Q00 1600 1800 2000 2200 2400 0200 0400 0600 0800 Numbers East Branch 2.8 2.7 5.3 4.8 3.7 5.0 23.7 14.1 23.7 9.3 2.5 2.5 Perkiomen 3.6 3.0 3.9 4.7 4.4 6.5 19.1 15.4 17.3 14.3 5.0 2.6 Biomass East Branch 2.3 2.0 3.0 4.3 3.0 4.3 32.2 15.0 20.3 8.0 2.3 1.7 Perkiomen 1.2 1.1 2.8 3.1 4.1 7.2 21.2 23.1 17.1 14.7 3.3 1.3 Taxa East Branch 8.0 7.2 7.4 7.7 8.0 8.0 12.3 12.3 12.0 8.3 5.4 3.2 Perkiomen 5.0 5.4 6.8 8.4 8.0 9.9 10.9 12.2 10.8 10.6 7.0 5.0 Ci) As an example, the highest numeric drift density (19.1%) on Perkiomen Creek generally occurs near 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br />.
LGS EROI TABLE 2.2-53 (Paqe 1 of 2)
FISBES(') COLLECTED IN PERIRIOMEN CREEK By ALL TYPES aF GEARS DUPING THE PERIOD JUNE 1970 THROUGH DECEMBER 1977 Relative Commn Name AtUndange SceniifJLS Name Fresbwater eel famil Anquillidae American eel anguill rostrata (Lesueur) Rare Trot famil Salmonidae Brook trout alvelilnuI fontinalis (Mitchell) Rare gike fZmi Eeocidae Redfin pickerel I=o americanus americanus (Gmelin) Un common Muskellunqe JZo masauinonov (Mitchill) Uncommon Cyprinidae Gold fish Caxius aurat+/-s (Linnaeus) Common Carp Qzrinu carpi (Linnaeus) Common Carp x Goldfish hybrid Uncommon Cutlips minnow Zalossum maxilligLu* (lesueur) Common Golden shiner gote+/-02ma crisoleuca (Mitchill) Uncommon Comely shiner Abundant Satinfin shiner M*roris analostangs (Girard) Abundant Bridle shiner royis tiLfrna (Cope) Rare Common shiner Vctrcois cornutu (Mitchill) Common Spottail shiner Notrovis hudonius (Clinton) Abundant Swallowtail shiner S rocne (Cope) Common Spotfin shiner NOtrovis stl outer I (Cope) Abundant Bluntnose minnow e bai nota (Rafinesque) Common Fathead minnow Pimehbales cromelas (Rafinesque) Rare Blacknose dace atratulus
_inicbtbs (Hermann) Common Lonqnose dace Thinib Smtlsatromaculatus
~bn cataractas (Valenciennes)
(Mitc~tll)
Common Creek chub Uncommon Fallfish Smtlscorrorali* (Mitcbill) Common Catostomidae White sucker catcstomus commersoni (Lacepedel Abundant Creek chubsucker Erivzon oblongus (Mitchill) Uncommon
IGS EROL TABlE 2.2-53 (Cont'd) (Paqe 2 of 2)
Relative Comm Name Abundance Freshwater catfish ai Ictaluridae White catfish Ictalurus catus (Linnaeus) Rare Yellow bullhead *_ctal-rus natalis (Lesueur) Common Brown bullhead _Tc2 uus nebulosus (tesueur) Un common Channel catfish _Ictalurus runctatus (Rafinesque) Rare Marqined madtom .otulrus insiqnis (Richardson) Uncommon Killifis famil Cyrinodontidae Banded killifisb Fundulus diarhanus (Lesueur) Common Mummi choq Fundulus beteroclitus (Linnaeus) Rare 2 Sungi~sh "gel~y Centrarcbidae Rock bass Ambloplites rupestris ((Rafinesque)) Common Redbreast sunfish l epomis auritus (Linnaeus) Abundant Green sunfish Lelomis cyanellus (Rafinesque) Common Pumpkinseed Leromis gittosus (Linnaeus) Common Blueqill L~eomis macrochirus (Rafinesque) Common Sunfish hybrid Le.pomis hvyrid Uncommon Smallmouth bass Microyterus dolomieui (Lacepede) Common Larqemouth bass Micropterus salmoides (Lacepede) Uncommon White crappie Pomoxis annularis (Rafinesque) Rare Black crappie Pomqxis niqromaculatus (Lesueur) Rare Percidae Tessellated darter Etbeostoma olmstedi Storer Common Shield darter Percina reltata (Stauffer) Uncommon I Nomenclature from Ref 2.2-53 2 Possible bait release.
0 IGS ERCI TAELE 2.2-54 MEAN rENSITY AND RELATIVE ABUNDANCE OF DRIFTING LARVAL FISH CCLLECIED FRCM PERKICMEN CREEK AT P14390, MAY THROUGH AUGUST 1973, 1974, ANr 1975.
1973 1974 1975 raxa- _ Nc. /Mi3 No. /m3 Nc. /M3 4innows 0.08028 36 0.06707 12.4 0.09465 34.5 2arp 0.11258 50.5 0.43283 79.9 0. 12685 4 6.3 bhite Sucker 0.0 1996 5.4 0.00775 1.4 0.01815 6.6 fellow Bullhead 0.00185 0.8 0.00223 0.4 0.00108 0.4 3anded Killifish 0.00012 Lepomis Sunfish 0.00923 4.1 0.03007 5.6 0.02096 7.6 ressellated Darter 0.00461 2.1 0.00047 0.1 0.00972 3.5 3hield Darter 0. 0C231 1 0.00117 0.2 0.00281 1 rotal 0.22285 0.54171 0.27424
LGS EROL TABLE 2.2-55 TOTAL CATCH AND RELATIVE ABUNDANCE OF LARVAL FISH COLLECTED BY TRAP NET FROM PERKIOMEN CREEK SHORELINE P14390, MAY THROUGH AUGUST 1975 Total %
Taxa Catch Catch Minnows 1270 83.0 Carp 18 1.2 White sucker 116 7.6 Lepomis sunfish 94 6.1 Tessellated darter 29 1.9 Shield darter 3 0.2 TOTAL 1530 TOTAL 1530
0 LGS EROL Page 1 of 2 TABLE 2.2-56 DAILY MEAN DENSITY (No./m 3 ) OF DRIFTING LARVAL FISH COLLECTED FROM PERKIOMEN CREEK AT P14390, MAY THROUGH AUGUST, 1974 AND 1975 1974 Taxa 08May 15May 20May 30May 05Jun 11Jun 27Jun Minnows 0.003 0.001 0.557 0.032 0.039 0.060 0.029 Carp 0.003 - 7.304 0.659 0.011 0.127 -
White sucker 0.024 0.042 - 0.003 - - -
Yellow bullhead - - - - - 0.003 Rock bass - - - 0.006 0.006 0.007 -
Lepomis sunfish - - 0.002 0.002 0.022 0.300 0.025 Tessillated darter 0.002 0.002 0.002 ....
Shield Darter 0.009 0.002 0.002 0.002 - -
LGS EROL Page 2 of 2 TABLE 2.2-56 (Cont'd) 1974 (Cont'd)
Taxa 02Jul 08Jul 16Jul 24Jul 29Jul 05Aug 13Aug 22Aug 27Aug Minnows 0.027 0.142 0.059 0.089 0.037 0.094 0.042 0.037 0.020 Carp - 0.003 0.006 0.006 0.003 0.057 - - -
White sucker ..- - - - -
Yellow bullhead - 0.038 0.006 ......
Rock bass - 0.005 - - - -
Lepomis sunfish - 0.025 0.019 0.039 0.118 0.035 - - -
Tessellated darter - - - - - -
Shield Darter -........
1975 Taxa 12May 27May 17Jun 01Jul 29Jul 12Aug 26Aug Minnows 0.087 0.055 0.006 .0369 0.069 0.016 0.003 Carp - 0.316 - - 0.001 - -
White sucker 0.155 0.011 .- -.
Yellow bullhead - - - 0.003 - - -
Rock bass - - - 0.011 - - -
Lepomis sunfish - 0.004 - 0.078 0.016 0.001 -
Tessellated darter 0.023 0.010 0.002 - - -
Shield Darter 0.019 0.001 -....
0 TGS EROL TAPLE 2.2-57 BCPIZCNIAL VARIATICN IN DENSITY OF LARVAL FISH COLLECTED FROM PERKIOMEN CREEK AT P14390 IN 1975 Net 1 2 3 4 5 6 Taxa Minnows 0.0584 0.0498 0.0481 0.0512 0.0098 0.0448 Carp 0.1494 0.1908 0.2549 0.2636 0.0366 0.0616 Wbite Sucker 0.0363 0.0420 0.0408 0.0035 0.0850 0.1473 Yellow Pulihead 0.0017 0.0009 0.0019 0.0010 0.0026 Rock Bass 0.0042 0.0067 0.0068 0.0024 0.0066 0.0216 Lepomis Sunfish 0.0234 0.0138 0.0094 0.0097 0.0038 0.0396 Tessellated Dartfish 0.0113 0.0160 0.0130 0.0204 0.0082 0.0075 Shield Darter 0.0128 0.0092 0.,0091 0.0109 0.0092 0.0068
LGS EROL TPEIE 2.2-58 MEAN DIRECT DENSITY OF LARVAL FISH IN THE EAST AND WEST CHANNELS CF PERKICMEN CREEK AT P14390 IN 1975 East Channel Vest Channel Taxa No./m3 No./M3 Minnows 0.0286 0.0521 Carp 0.0508 0.2103 White Sucker 0.1117 0.0404 Yellow Bullhead 0.0011 0.0014 Rock Bass 0.0161 0.0050 Lepomis Sunfish 0.0217 0.0146 Tessellated Darter 0.0080 0.0150 Shield Darter 0.0082 0.0106
0 LGS EROL TABLE 2.2-59 Page 1 of 2 ANNUAL AND SPATIAL VARIATION IN'IEAN CATCH-PER-UNIT-EFFORT (C/F, AND RELATIVE ABUNDANCE OF FISH COLLECTED BY SEINE FROM THE PERKIOMEN CREEK IN 1975 AND 1976) 1975 1976 1975 1976 1975 1976 1975 1976 P19775 P19775 P16500 P16500 P14455 P14455 P14320 P14320 Species C/F % C/F % C/F % C/F % C/F % C/F % C/F % C/F American eel 0.10 0.1 - - - --
Cutlips minnow 1.23 0.8 .0.09 0.1 0.88 0.5 - - -
Golden shiner - - 0.18 0.1 0.08 0.1 - - - - 1.60 0.3 - - 0.13 Comely shiner 25.70 25.2 3.59 2.2 2.90 4.1 2.67 1.7 1.92 1.4 20.49 4.0 3.64 2.5 5.39 Satinfin shiner 1.06 1.0 2.96 1.8 7.44 10.5 18.68 11.6 0.64 0.5 1.89 0.4 3.76 2.6 7.95 Common shiner 1.97 1.9 4.00 2.4 0.61 0.9 3.13 1.9 1.62 1.2 0.60 0.1 0.86 0.6 0.61 Spottail shiner 2.27 2.2 26.68 16.3 0.48 0.7 44.94 27.8 3.39 2.5 80.60 15.7 2.09 1.5 27.81 Swallowtail shiner 9.48 9.3 4.06 2.5 1.68 2.4 4.53 2.8 1.82 1.4 6.74 1.3 54.24 37.7 1.30 Spotfin shiner 56.60 55.4 71.18 43.4 53.12 74.8 66.35 41.1 115.33 85.7 360.72 70.4 71.09 49.4 222.34 Bluntnose minnow 0.30 0.3 0.10 0.1 0.47 0.7 0.56 0.3 1.03 0.8 8.60 1.7 0.36 0.2 0.13 Blacknose dace - - 0.43 0.3 0.30 0.4 1.06 0.7 - - - - - - 0.26 Longnose dace 0.89 0.9 5.23 3.2 0.10 0.1 0.65 0.4 .-
Creek chub 0.39 0.2 - - 0.30 0.2 - -
Fallfish 1.79 1.8 0.26 0.2 0.20 0.3 0.48 0.3 - - 0.14 0.1 White sucker - - 26.88 16.4 0.30 0.4 7.92 4.9 - - 1.60 0.3 0.14 0.1 4.96 Yellow bullheaad - - 0.10 0.1 - - 0.09 0.1 - - - - -
Brown bullhead - - 0.08 0.1 ...- -.
Margined madtom - - - - - - 0.08 - - - - - -
Banded killfish 0.27 0.3 0.51 0.3 0.39 0.6 1.59 1.0 - 0.34 0.1 0.80 0.6 0.50 Rock bass 0.12 0.1 0.26 0.2 0.20 0.3 0.09 0.1 - - 0.40 0.1 0.50 0.4 -
Redbreast sunfish - - 0.81 0.5 2.05 2.9 1.72 1.1 3.22 2.4 9.77 1.9 2.73 1.9 2.33 Green sunfish 0.09 0.1 - - - - 0.20 0.1 0.81 0.6 4.80 0.9 - - 0.26 Pumpkinseed - - - - - - - 2.5 1.5 6.17 1.2 0.45 0.3 0.49 Bluegill 0.12 0.1 0.09 0.1 0.29 0.4 2.30 1.7 2.97 0.6 1.72 12 Lepomis hybrid - - - - - 0 Smallmouth bass 0.12 0.1 4.52 2.8 0.29 0.4 4.92 3.0 0.14 0.1 3.60 0.7 1.24 0 7.27 Largemouth bass 0.09 0.1 0.61 0.4 - - 0 White crappie - - - - - - - 0 0 0 0.14 0.1 0.59 Tessellated darter 1.07 1.0 9.52 5.8 - - 0.33 0.2 0.22 0.2 1.20 .2 0.17 0.1 - - 0.25 0.2 - - 0.20 - - - -
Shield darter 0.12 0.1
LGS EROL Page 2 of :
TABLE 2.2-59 (Cont'd) 1975 1976 1975 1976 1975 1976 Years P14130 P14130 P13580 P13580 Mean Mean Mean Species % C/F % C/F % C/F % C/F % C/F % C/F % C/F %
American eel - - - - - - - - 0.02 - 0.01 -
Cutlips minnow 0.21 0.33 - - 0.22 0.2 0.63 0.2 0.09 0.1 0.46 0.2 0.28 0.1 Golden shiner - - 0.34 0.1 0.40 0.3 0.39 0.1 0.08 0.1 0.42 0.2 0.25 0.1 Comely shiner 1.9 0.57 0.7 6.23 2.3 2.16 1.77 3.23 1.0 6.25 5.7 6.73 2.4 6.49 3.3 Satinfin shiner 2.8 11.22 13.4 13.98 5.2 9.58 7.6 7.56 2.4 5.73 5.2 8.94 3.2 7.33 3.8 Common shiner 0.2 5.03 6.0 2.63 1.0 8.05 6.4 2.71 0.9 3.08 2.8 2.31 0.8 2.69 1.4 Spottall shiner 9.8 4.11 4.9 24.98 9.3 5.17 4.1 24.50 7.8 2.92 2.7 37.60 13.4 20.26 10.4 Swallowtail shiner 0-.5 0.54 0.6 1.92 0.7 2.11 1.7 1.99 0.6 11.13 10.2 3.37 1.2 7.25 3.7 Spotfin shiner 78.7 59.30 70.6 197.47 73.7 91.62 73.0 212.41 67.6 73.93 67.7 185.76 66.3 129.84 66.7 Bluntnose minnow - - 0.47 0.2 1.29 1.0 9.31 3.0 0.57 0.5 3.11 1.1 1.84 0.9 Blacknose dace 0:1 - - 4.66 1.7 0.53 0.4 1.99 0.6 0.14 0.1 1.42 0.5 0.78 0.4 Longnose dace - - 1.36 0.5 - - 0.23 0.1 0.17 0.2 1.26 0.5 0.72 0.4 Creek chub -- - - - - - 0.37 0.1 - - 0.18 0.1 0.09 -
Fallfish 0.48 0.6 0.34 0.1 0.22 0.2 0.34 0.1 0.49 0.4 0.24 0.1 0.36 0.2 White sucker 1.8 0.11 0.1 10.68 4.0 - - 21.80 6.9 0.09 0.1 12.47 4.4 6.28 3.2 Yellow bullheaad - - - - - 2.23 0.7 - - 0.41 0.1 0.21 0.1 Brown bullhead - - - 0.01 - 0.01 -
Margined madtom - - - 0.11 - - - - - 0.03 - 0.02 -
Banded killfish 0.2 0.97 1.2 1.08 0.4 1.21 1.0 2.89 0.9 0.61 0.6 - 1.17 0.4 0.89 0.5 Rock bass -- - - - 0.09 0.1 0.08 - 0.15 0.1 0.13 - 0.14 0.1 Redbreast sunfish - - 0.81 0.5 2.05 2.9 1.72 1.1 3.22 1.58 1.4 3.14 1.1 2.36 1.2 Green sunfish 0.09 0.1 - - - - 0.20 0.1 0.81 0.22 0.2 1.40 0.5 0.81 0.4 Pumpkinseed -- - - - 2.5 0.43 0.4 1.77 0.6 1.10 0.6 Bluegill - - - - 0.92 0.3 0.70 0.6 0.63 0.2 0.66 0.3 Lepomis hybrid - 0.10 0.1 - - 0.11 0.1 - - 0.04 - - - 0.02 -
Smallmouth bass 2.6 0.42 0.5 0.57 0.2 0.43 0.3 1.58 0.5 0.43 0.4 3.75 1.3 2.09 1.1 Largemouth bass 0.1 - - - - - - 0.16 0.1 0.02 - 0.18 0.1 0.10 0.1
- - - - - - - 0.08 - - - 0.01 - 0.01 -
White crappie Tessellated darter 0.2 0.33 0.4 0.73 0.3 0.39 0.3 6.25 2 0.36 0.3 3.13 1.1 1.75 0.9 Shield darter - 0.09 0.1 - - - - 0.42 0.1 0.04 - 0.17 0.1 0.10 0.1
IGS EROL TABIE 2.2-60 ANNUAL VARIATION AND FREQUENCY OF OCCURRENCE (FO) IN AGE 0 SUNFISH SPECIES COLLECTED BY ELECTPOFISHING IE PERKICMEN CFEEK (ALL SITES COMBINED) IN 1975 AND 1976 1975 1976 Grand Total % FC Total FO Total %
Srecies Catch Total M Catch Total M Catch Tctal Rock bass 4 3.5 25.0 14 4.9 50.0 18 4.5 Redbreast sunfish 64 56.6 100.0 197 69.6 100.0 261 65.9 Green sunfish 41 36.3 83.3 36 12.7 58.3 77 19.4 Pumpkinseed - - - 34 12.0 50.0 34 8.6 Smallmouth bass 4 3.5 25.0 2 0.7 8.3 6 1.5 Tot al 113 263 396
LGS EROL TABLE 2.2-61 MONTHLY VARIATION IN MEAN CATCH-PER-UNIT EFFORT OF FISH COLLECTED BY SEINE FROM PERKIOMEN CREEK (ALL SITES COMBINED) IN 1975 AND 1976)
Feb Mar Apr May Jun Jul Species 1975 1976 1975 1976 1975 1976 1975 1976 1975 1976 1975 American eel - - - - - - - - - -
Cutlips minnow - - - - 0.20 - 0.41 1.04 0.16 Golden shiner 0.21 - 0.15 - 0.20 0.14 2.57 0.20 - 0.17 Comely shiner 38.44 1.07 0.35 1.67 17.03 2.21 7.05 4.39 1.51 0.14 2.81 Satinfin shiner 1.29 0.81 3.64 0.47 2.39 11.34 2.82 11.42 2.05 2.77 4.38 Comnon shiner 1.41 - 0.17 - 8.26 - 2.92 - 5.75 7.31 9.50 Spottall shiner 0.75 0.24 3.08 - 4.45 - 5.58 0.21 7.61 225.33 5.78 Swallowtail shiner 2.19 0.36 0.28 0.13 2.02 0.42 87.54 3.46 0.57 3.64 -
Spotfin shiner 52.22 2.65 18.24 2.20 99.76 14.20 131.20 71.04 52.80 64.86 17.08 Bluntnose minnow 0.63 - 0.99 - 1.55 0.14 0.87 0.28 - 0.56 -
Blacknose dace .- - 0.56 3.10 - 1.98 0.81 3.09 0.17 Longnose dace - - - 0.33 0.15 1.07 0.30 0.22 8.45 -
Creek chub - - - - - 0.15 -
Fallfish 0.26 0.26 0.33 1.54 1.09 - 1.04 1.02 0.65 White sucker - - - - 0.56 3.81 0.45 40.69 -
Yellow bullhead - - - -
Margined madtom - - - - - - - -
Banded killfish 0.31 0.45 1.64 0.41 2.92 0.21 0.61 0.60 - 1.20 -
Rock bass - - - - - - 0.41 0.14 0.24 0.15 0.19 Redbreast sunfish - - - 0.48 1.31 1.63 0.56 3.37 1.25 0.34 Green sunfish 0.25 - - - 0.56 - 0.20 0.28 0.24 Pumpkinseed - - 0.28 0.28 - 0.20 0.14 2.29 0.47 0.37 Bluegill - - - 0.28 - 2.02 - 1.38 Lepomis hybrid - - - 0.20 - - -
Smallmouth bass - 0.24 - - 0.82 - 30.47 0.37 Largemouth bass 0.25 .- - 0.14 - -
White crappie - - - - - -
Tessellated darter 0.23 0.92 0.33 0.57 0.59 0.20 - 0.79 14.91 -
Shield darter - - - - 0.13 - 0.33 0.22 0.86 -
Aug Sep Oct Nov Dec Species 1976 1975 1976 1975 1976 1975 1976 1975 1976 1975 1976 American eel 0.19 - - - - - - - -
Cutlips minnow 2.11 0.19 1.04 - 0.67 - 0.17 -
Golden shiner 0.67 0.42 - 0.15 - 0.21 - 0.42 - -
Comely shiner 4.24 2.00 9.10 4.49 16.54 2.28 18.69 0.89 12.70 2.68 2.12 Satinfin shiner 4.96 6.26 11.59 9.85 10.46 5.93 15.05 8.60 16.37 14.31 11.83 Common shiner 8.40 3.88 3.42 0.83 2.59 0.61 0.50 - 0.85 - 1.91 Spottail shiner 47.31 1.33 24.69 1.00 49.40 1.52 30.17 0.19 14.24 0.17 15.76 Swallowtail shiner 0.46 2.79 3.32 3.44 9.93 0.97 10.34 1.92 3.59 17.78 0.88 Sptfin shiner 59.24 66.73 187.98 181.62 426.96 60.60 631.47 59.56 502.87 66.17 48.92 Bluntnose minnow 2.00 0.28 0.50 0.64 7.71 - 7.92 0.30 14.45 1.06 0.17 Blacknose dace 1.43 - 2.76 - 0.87 - 0.42 - 0.76 - -
Longnose dace 1.46 - 0.19 - 0.15 - - - - - 0.14 Creek chub 1.32 0.37 - - 0.19 - 0.51 - - - -
Fallfish 0.63 - 2.53 - 0.30 - 0.67 - 0.14 -
White sucker 6.88 - 0.72 - 0.19 - - - - -
Yellow bullhead 3.54 - - - 0.21 - 0.14 - - - -
Margined madtom - 0.32 1.76 0.49 1.62 0.21 1.49 - 2.24 0.17 1.19 Banded killfish 1.51 - 0.50 0.58 1 0.19 0.33 - 0.33 - -
Rock bass - 2.11 13.46 6.72 6.57 0.42 2.64 1.76 - - -
Redbreast sunfish 8.30 0.16 9.54 0.50 1.16 0.56 1.51 - 0.81 - -
Green sunfish 1.88 0.14 1.41 0.33 4.76 - 8.30 0.67 2.83 0.28 -
Pumpkinseed 1.04 0.52 1.33 1.42 - 0.83 2.89 1.00 - 0.28 -
Bluegill 2.29 0.19 - - - - - - - - -
Lepomis hybrid - 1.58 2.96 0.38 0.97 0.21 0.15 0.39 -
Smallmouth bass 6.02 - - - - - 0.15 - -
Largemouth bass - - - - 0.15 - - - -
White crappie - 0.35 1.85 - 2.80 - 2.03 0.71 1.57 0.19 1.12 Tessellated darter 8.76 - - 0.19 - - - - 0.17 Shield darter 0.35
LGS EROL TABLE 2.2-62 TOTAL CATCH AND RELATIVE ABUNDANCE OF FISHES COLLECTED BY ELECTROFISHING FROM PERKIOMEN CREEK IN 1974, 1975, AND 1976 1974 1975 1976 P14390 P14160 P14020 P14160 P20000 P14390 P14160 P14020 Total Total Species No. % No. % No. % No. % No. % No. % No. % No. % No. %
American eel 7 0.3 2 0.3 1 0.1 4 0.4 7 0.6 9 0.4 5 0.7 2 0.3 37 0.4 Muskellunge (1) - (1) 1 0.1 - (1) 2 0.2 - (1) - (1) - (1) 3 (1)
Goldfish 13 0.6 - (1) (1) - 1 4 0.4 17 0.7 - (1) 34 0.4 Carp 137 6.2 18 2.4 42 6.1
-34 (1) 5.4 464 4.9 11 1.1 105 9.2 104 4.4 13 1.7 Golden shiner (1) (1)
(() 3 0.3 - (1) - (1) - (1) 3 (1)
Fall fish 1 (1) (1) (1) 7 0.7 (1) - (1) - (1) 8 0.1 Minnow hybrid 6 0.3 - (1) 4 0.6 2 0.2 3 0.3 - (1) - (1) 15 0.2 White sucker 241 10.8 50 6.6 59 8.5 101 10 272 23.9 215 9.1 123 16.4 99 15.8 1160 12.1 White catfish - (1) - (1) - (1) (1) 1 (1) 1 (1)
- 0.1 - (1) - (1)
Yellow bullhead 68 3.1 17 2.2 9 1.3 30 3 33 2.9 43 1.8 11 1.5 4 0.6 215 2.2 Brown bullhead 34 1.5 2 0.3 5 0.7 1 0.1 6 0.5 19 0.8 1 0.1 1 0.2 69 0.7 Channel catfish - (1) - (1) - (1) - (1) 1 0.1 1 (1) - (1) (1) 2 (1)
Margined madtom 15 0.2 5 0.2 2 0.3 - (1) 1 0.1 1 0.1 6 0.3 - (1)
Rock bass 88 4.0 36 4.8 26 3.8 65 6.5 67 5.9 99 4.2 33 4.4 29 4.6 443 4.6 275 43.9 4656 48.7 Redbreast sunfish 993 44.7 507 67.1 333 48.1 510 50.7 408 35.9 1172 49.6 458 60.9 Green sunfish 127 5.7 19 2.5 48 6.9 30 3 36 3.2 116 4.9 22 2.9 27 4.3 425 4.4 Pumpkinseed 130 5.9 13 1.7 37 5.3 59 5.9 43 3.8 164 6.9 12 1.6 47 7.5 505 5.3 Bluegill 89 4.0 8 1.1 12 1.7 91 9 35 3.1 49 2.1 3 0.4 26 4.2 313 3.3 Lepomis hybrid 24 1.1 2 0.3 3 0.4 3 0.3 7 0.6 23 1 9 1.2 3 0.5 74 0.8 Smallmouth bass 254 11.4 79 10.4 108 15.6 87 8.6 90 7.9 324 13.7 62 8.2 78 12.5 1082 11.3 Largemouth bass 5 0.2 1 0.1 5 0.7 1 0.1 8 0.7 2 0.1 - (I) 1 0.2 23 0.2 White crappie (1) 5 (1) 4 (1)
(11 (1) (1) 0.4 - - (1) - (1) 5 0.1 Black crappie (1) 5 0.4 - (1) - (1) 2222 756 693 1006 1138 2363 752 626 9556 Total
( 1 )Less than 0.1%
IGS ERCI TAPLE 2.2-63 CRITERIA FOP DETERMINATION OF IMPORTANT FISHES CF PERKIOMEN CREEK IMPORTANCE LINK TO PLANT DIRECT Susceptible Susceptible to to Common Name Commercial Recreational Ecological Abundant Impingement Entrainment American shadi x x 'I MuskellunqeR x Carp,,).' x x x x x Comely shiners x x x x Spottail shiner3,4,$ x x x Spotfin sbiner'.'.5 x x x x White sucker',3,4,5,6 x x x x x Redbreast sunfishz,3.4,6,6,7 x x x x x x Smallmouth bass2,5,6,7 x x x x Shield darter3,4,S x x x
'Importance dependent on results of Pennsylvania Fish Commission program to provide fishways at dams downriver of GS.
ESpecies sampled by large fish pcpulation estimate program.
3Species sampled by larval fish drift program.
4Species sampled by larval fish trap net program.
5Species sampled by seine proqram.
'Species sampled by aqe and qrowth proqram.
?Species sampled by small fish pcpulation estimate program.
LGS EROL TABLE 2.2-64 ANNUAL AND SPATIAL VARIATION IN REDBREAST SUNFISH POPULATION ESTIMATES AT FOUR SITES ON PERKIOMEN CREEK IN 1975 AND 1976 19751 1976 Site No/20 m No/20 m P14830 53 P14690 75 P14225 24 P14210 49 Streamwide estimate 81 185
'Too few specimens were captured in 1975 to provide reliable estimates for the sites.
IGS ERCI TABLE 2.2-65 POPULATION ESTIMATES (No PER HECTARE) AND ESTIMATED BICNASS (WQt PER HECTARE) OF LARGE FISHES COLLECTED BY ELECIPOFISBING FROM FOUR SITES ON PERKIOMEN CREEK IN 1974, 1975, AND 1976 P20000 P14390 P14160 P14020 lNo/ha Wt/ha No/ha lt/ba No/ha Ut/ha No/ha sit/ba Species Year (kq) (kg) (kg) (kq)
Redtreast sunfish 1974 - - 437 20.9 1622 55.3 897 -
1975 - - - - 1479 46.5 - -
1976 5415 14.5 338 18.7 1397 54.3 511 25.e Carp 1974 - - 110 208.0 41 90.1 - -
1975 - - - -
1976 131 160.0 67 95.0 white sucker 1974 - - 154 80.4 174 1149.0 137 -
1975 - - - - 451 110.0 - -
1976 314 175.0 139 58.1 334 90.8 258 67.E Green sunfish 1974 - - 87 2.12 1975 - - -
1976 18(l) 0.743 36 1.21 Smallmouth bass 1974 - - 53 5.69 1975 - - - 210 7.72 - -
1976 29(s) 2.717 84 7.29 163 12.4 - -
(1) Represents fish considered to be >aqe 1.
(8) Represents fish considered to be age 2.
LGS EROL TABLE 2.2-66 POPULATION ESTIMATES BY AGE-GROUP FOR REDBREAST SUNFISH COLLECTED FROM FOUR SITES ON PERKIOMEN CREEK IN 1974, 1975, AND 1976 YEAR Site Age-Group 1974 1975 1976 P20000 I - - 350 II - - 156
>II - - 169 Total - - 675 P14390 I 734 - 247 II 519 - 580
>II 578 - 591 Total 1831 - 1418 P14160 I 438 360 313 II 406 403 397
>II 177 137 167 Total 1021 900 877 P14020 I 214 - 85 II 332 - 174
>II 165 - 143 Total 711 - 402
LGS EROL TABLE 2.2-67 LENGTH-WEIGHT RELATIONSHIPS(1) OF IMPORTANT SPECIES COLLECTED BY SEINE FROM PERKIOMEN CREEK IN 1975 AND 1976 Species Site/Year a b Comely shiner P19775 -12.57 3.23 P16500 -11.83 3.05 P14455 -11.52 2.96 P14320 -11.19 2.92 P14130 -10.84 2.78 P13580 -10.95 2.82 1975 -12.00 3.09 1976 -11.05 2.85 Spottail shiner P19775 -11.63 3.04 P16500 -11.75 3.09 P14455 -11.82 3.08 P14320 -12.43 3.25 P14130 - 9.94 2.63 P13580 -11.58 3.03 1975 -12.82 3.33 1976 -11.09 2.91 Spotfin shiner P19775 -12.03 3.12 P16500 -11.93 3.11 P14455 -12.18 3.17 P14320 -12.43 3.24 P14130 -12.49 3.26 P13580 -12.10 3.16 1975 -12.39 3.22 1976 -12.08 3.16 (1) in W = a+b In L.
0 TGS EROL TABLE 2.2-68 MEAN CALCULATED LENGTHS AT ANNULUS FOP REBCREAST SUNFISH, WHITE SUCKER, AND SMALLMOUTH BASS COLLECTED FROM PERKICMEN CREEK IV 1973 AWD 1976 No. of Weiabted Mean Lenath (mm ILlat Annulus Species Year Site Fish I II III IV V Redbreast sunfish 1973 Streamwide 208 41 90 127 150 166 Red reast sunfish 1976 P20000 64 35 76 117 147 -
P14390 63 43 88 130 156 -
P11160 62 37 85 122 - -
P14020 55 38 86 125 145 -
Population Mean 38 814 124 1419 -
White sucker 1976 P20000 43 113 213 291 - -
P14390 31 111 213 293 - -
P14160 43 107 206 259 - -
P14020 341 98 178 263 - -
Population Mean 107 203 277 - -
Smallmouth bass 1973 Streamwide 76 83 159 213 - -
LGS EROL TABLE 2.2-69 LENGTH-WEIGHT RELATIONSHIPS"*)
FOR WHITE SUCKER COLLECTED BY ELECTROFISHING AT FOUR SITES ON PERKIOMEN CREEK IN 1976 Site a b P20000 -10.11 2.81 P14390 -10.72 2.91 P14160 -11.25 3.01 P14020 -11.71 3.09 (1) in W = a+b in L.
LGS ERPO TABLE 2.2-70 (Page 1 of 3)
NUMBER OF SAMPLES BY YEAR, PROGRAM, AND SITE COLLECTED FROM EAST BRANCH PERKICNEN CREEZ, 1972 THROUGH 1977 (1)
Program/Sites 127. 1973 197-4 12-71 1977 Water Quality, A11263 - - 14 24 24 24 E32300 - " 14 24 24 24 P26700 - - 14 24 24 24 E22880 - - 14 24 24 24 E2800 - - 14 24 24 24 Periphyton E32115 - - 29 - - -
E22867 - - 26 - - -
E8350 - .14 - -.
E2800 - 14 26 - - -
Benthic Macroinvertebrates E36725 9 12 9 - 10 -
E32200 12 12 9 - 10 -
E26700 12 12 9 - 11 -
E23000 9 12 9 - 11 -
112500 12 12 9 - 11 -
E5600 12 12 9 - 11 -
Macroinvertebrate Drift E2230 - 84 69 - -
larval Fish Drift E2650 - 136 56 - -
Seine E36690 - - - 10 10 -
E32170 - - - 11 10 -
E29810 - - - 11 10 -
E26630 - - - 11 10 -
E22980 - - - 11 10 -
E12440 - - - 11 10 -
£5475 - - - 11 10 -
E1890 - - - 11 10 -
Larqe Fish Population Estimates E36020 - 2 - 2 - -
E30540 - 2 - 2 - -
E22240 - 2 - 2 - -
E15500 - - 2 2 - -
E12040 - 2 - 2 - -
E5650 - - 2 2 - -
E1550 - 2 - 2 - -
LGS EROL TABLE 2.2-70 (Cont'di (Paqe 2 of 3)
ProgrAM/Sites .1922 .1973 1974 17 1977 Aqe and Growth F10235C2)
Redfin pickerel 2 E36700 Redbreast sunfish I E36020 Redfin pickerel - ' 24 White sucker - 33 Redbreast sunfish - l46 29 Green sunfish - 50 36 E34350 Redbreast sunfish - 36 Green sunfish - 116 E34250 Redbreast sunfish - 8 E32300 Redbreast sunfish - 33 Green sunfish - 31 E32200 Redbreast sunfish - 11 Green sunfish - 2 E31290 Redfin pickerel - I E30940 Redbreast sunfish - 39 Green sunfish - 22 E30540 Redfin pickerel - 11 White sucker - 1O0 Redbreast sunfish - 56 56 Green sunfish - 35 39 E26700 Green sunfish - 2 E22240 Redfin pickerel - 1 White sucker - 28 Redbreast sunfish - q14 211 Green sunfish - 67 50 E18400 Redbreast sunfish - 5 Green sunfish - 16 E18340 Redbreast sunfish - 2 Green sunfish - 33 E12040 White sucker - 20 Redbreast sunfish - 35 - l46 Green sunfish - 60 - 36
LGS EROI TABLE 2.2-70 (Cont'd) (Paqe 3 of 3)
Program/Sites IM1 am 1.974 197 I=1. 1977 Aqe and Growth (cont.)
E10700 Redbreast sunfish - 19 Green sunfish - 55 E8500 Redbreast sunfish - 34 Green sunfish - 118 E7100 White sucker - 25 Redbreast sunfish - 17 Green sunfish - 34 E2100 Redbreast sunfish - 37 Green sunfish - 25 E1550 White sucker - 26 Redbreast sunfish - 56 55 Green sunfish - 32 43
(')See footnotes in Table 2.2-7 for definition of what constitutes one sample.
(2)Culvert Creek, a tributary of East Branch Perkiomen Creek.
Collection site approximately 235 m from East Branch confluence.
LGS EROI TABLE 2.2-71 NUMBER OF SPAPLES BY MONTH, PROGRAM, AND YEAR CCLLECTED FROM EAST FPANCH PERXIOMEN CREEK, 1972 THROUGH 1977 (1)(8)
Jan W bLax = la !bw 9SA us =
Water Quality 1974 10 10 10 10 10 10 10 1975 10 10 10 10 10 10 10 10 10 10 10 10 1976 10 10 10 10 10 10 10 10 10 10 10 10 1977 10 10 10 10 10 10 10 10 10 10 10 10 Periphyton 1973 . . . . . 6 6 8 4 4 1974 - 12 6 5 15 3 8 9 9 9 5 Benthic Macroinvertebrates 1972 5 5 5 6 6 6 6 5 5 5 6 6 1973 6 6 6 6 6 6 6 6 6 6 6 6 1974 6 6 6 6 6 6 6 6 6
1976 6 6 6 6 6 6 6 4 6 6 6 Macroinvertebrate Drift 1973 - - 12 12 12 12 12 12 - -
1974 - - 12 12 12 9 12 - - -
Larval Fisb Drift 1973 - - 24 24 28 24 24 12 - -
1974 - - 6 14 12 14 10 - - -
Seine 1975 - 7 8 8 8 8 8 8 8 8 8 8 1976 - 8 8 8 8 8 8 8 8 8 8
(')See footnotes in Table 2.2-7 for definition of what constitutes one sawple.
(R)The samples for small Fish Population Estimate, Large Fish Population Estimate, and Aqe and Growth proqrams are not included because they are only collected on an annual basis.
LGS EFOL TAELE 2.2-72 (Paqe I of 2)
PERIPHYTON STANDING CRCP BICMASS (MG/DM2) ASH-FREE DRY %EIGHT AND PRODUCTIVITY PATES (MG/DMZ/DAY) ASH-FREE DRY %EIGH BY STATION IN EAST BRANCH PERKIOMEN CREEK, 1973 AND 1974 E32115 E22867(43 18350(s) E2800(6)
Days( I ) SC(a) sc P -C_n 17 Auq 1973 10 17.9 -(7) 14.0 24 Auq 17 39.7 3.11 19.3 0.76 31 Auq 24 48.4 1.24 42.0 3.24 7 Sep 7 14.3 10.8 10 Sep 14 18.4 0.59 21.4 1.51 21 Sep 21 11.8 -0.94 23.9 0.36 5 Oct 7 11.8 4.9 12 Oct 14 42.0 4.31 10.5 0.80 19 Oct 21 48.1 0.87 17.9 1.06 26 Oct 7 14.4 3.4 2 Nov 14 14.5 0.01 6.3 0.41 9 Nov 21 17.8 0.47 8.4 0.30 12 Dec 12 3.3 3.0 19 Dec 19 3.3 0.00 2.6 -0.06 1 Feb 1974 7 4.0 0.57 2.0 0.29 4.3 0.61 7 Feb 14 6.8 0.20 3.4 0.10 5.2 0.06 14 Feb 21 13.8 0.33 3.9 0.02 7.4 0.10 21 Feb 28 15.0 0.04 3.3 -0.20 8.6 0.04 14 Mar 7 3.3 0.47 4.0 0.57 5.4 0.77 21 Mar 10 4.0 0.05 4.1 0.01 7.5 0.15 18 Apr 7 4.1 0.58 3.7 0.53 5.3 0.76 24 Apr 14 20.8 1.19 net() nlu 81.5 5.44 2 May 7 25.9 3.70 42.6 6/09 14.5 2.07 9 May 14 32.7 0.48 40.2 -0.17 09.8 2.52 16 May 21 19.2 -0.64 27.5 -0.60 36.6 -0.63 23 May 7 7.4 1.05 15.7 2.24 16.0 2.57 31 May 14 19.7 0.60 28.4 0.95 30.5 0.89 6 Jun 21 35.2 0.74 62.0 1.60 45.3 0.70 no.
8 Auq 7 59.1 8.44 43.4 6.20 15 Auq 14 19.7 -2.81 77.3 2.42 49.5 3.54 23 Auq 22 106.3 4.22 55.5 -0.99 22.8 -1.27 12 Sep 7 13.4 1.91 13.0 1.86 12.5 1.78 20 Sep 15 18.5 0.34 18.6 0.37 04.4 2.13 26 Sep 21 27.9 0.45 27.2 0.41 37.9 -0.31 10 Oct 7 5.1 0.73 n8 nf 4.5 0.64 18 Oct (81(e)15 9.7 0.31 3.3 0.41 7.7 0.23 24 Oct 414) 21 14.2 0.21 17.7 1.03 4.4 -0.16 31 Oct (21) no nf 23.3 0.27 no9 rnu 14 Nov 7 3.3 0.47 4.8 0.69 1.9 0.27 21 Nov 14 8.0 0.34 9.1 0.31 3.8 0.14 28 Nov 21 15.1 0.36 19.3 0.51 5.4 0.08 12 Dec 7 0.60 0.09 0.20 0.03 0.20 0.03 19 Dec 14 0.80 0.01 n8 no nou no Dec no no9 27 21 2.50 0.08 no nf
LGS EROL TABLE 2.2-72 (Cont'd) (Paqe 2 of 2)
(')This represents the actual number cf days that the artificial plates are exposed to periphyton colonization.
(R)Standinq crop.
(B)Productivity rate.
C()Station E22867 was not sampled in 1973.
(C)Station E8350.was sampled only in 1973.
(')Station E2800 was not sampled in 1973.
(?)No values were calculated for periphyton productivity rates for any station in 19.73 due to low qrowth rates durinq the first 7 days of colonization.
(O)ns indicates that no samples were collected on that date.
(')The numbers in parenthesis indicate the number of days of exposure for the artificial plates at station E22867 only.
0 LGS ERCI TABLE 2.2-73 (Paqe 1 of 2)
FISHES COLLECTEC IN THE EAST BRANCH PERKIOMEN CREEK BY TYPES CF ALL GEARS DURING TEE PERIOD JUNE 1970 THROUGH DECEMBER 1976 (1)
. . EMS Relative Abundance Freshwater del Anquillidae American eel Ainuilla rostrata (Lesueur) Uncommon Salmonidae Brook trout Salvelinus fontinalis (Mitchell) occur only when stocked Psocidae Redfin pickerel ii.Qz americanus amer canus (Gmelin) Common Muskellunqe ZggM masguinonag (Nitcbill) Rare Chain pickerel X&M~ niger (Lesueur) Rare finno- aAmi Cyprinidae Goldfish Carassi auratus (innaeus) Common Carp Cvrrinue ca.r (Linnaeus) Common Carp x Goldfish hybrid Rare Cutulps minnow Exolossuj mexillingua (Lesueur) Abundant Golden shiner Hotemigonus crvgoleucas (Mitchill) Abundant Comely shiner Notropis amoenus (Abbott) Abundant Satinfin shiner Notosao analostanus (Girard) Abundant Bridle shiner NotrOzia bifrenatus (Cope) Uncommon Common shiner Notrovi cornutus (Mitchill) Abundant Spottail shiner Notropihudsonius (Clinton) Common Swallowtail shiner NotrQvi Procne (Cope) Abundant Spotfin shiner Notrovis spilocerus (Core) Abundant Bluntnose minnow Pimephale notatu$ (Rafinesque) Abundant Fathead minnow Pimephale promelas Rafinesque Rare Blacknose dace Rhinichthys atratulus (Hermann) Abundant Lonqnase dace Rbinishys cataractae (Valenciennes) Abundant Creek chub semotilus atromaculatuýs (Mitchill) Uncommon Fallfish Sematilus corporalis (*Litchill) Uncommon Minnow hybrid Rare
LGS FPOL TABLE 2.2-73 (Cont'd) (Paqe 2 of 2) scientific M Relative AbunQance Catostomi dae White sucker Catostomu commersoni (Lacepede) Abundant Creek chubsucker Eximvzon oblonglus (Mitchill)
Common Freshwater catfish family Ictaluridae White catfish Ictaluru catus (Linnaeus) Rare Yellow bullhead Ictalurus natalis (Lesueur) Abundant Brown bullhead Ictalurus nebulosu (Lesueur) Common Marqined madtom Noturu Insinis (Richardson) Common Cyrinodontidae Banded killifish Fundgl]uz .dLapnbsga (Lesueur) Abundant Centrarchidae Rock hass Amblonli2te runestris (Rafinesque) Common Redbreast sunfish Lejomis auritus (Linnaeus) Abundant Green sunfish LeDomis cyanellus Rafinesque Abundant Pumpkinseed Leomisi ibbosus (Linnaeus) Abundant Blueqill LeDomis macrochirus Rafinesque Common Sunfish hybrid Lepomis hybrid Abundant Smallmouth bass M dolomieui Lacepede Common Larqemouth bass Hicro(terus salmodes (Lacepede) Common White crappie Pomoxi annularis rafinesque Rare Percidae Tessellated darter Etbeostoma olstedi Storer Abundant Yellow perch Perc flavescens (Mitchill) Rare Shield darter Percil Deltata (Stauffer) Uncommon (I)Nomenclaturee from Ref 2.2-53.
LGS EROL TABLE 2.2-74 MEAN DENSITY AND RELATIVE ABUNDANCE OF DRIFTING LARVAL FISH COLLECTED FROM EAST BRANCH PERKIOMEN CREEK AT E2650, MAY-AUGUST IN 1973 and 1974 1973 1974 Taxa No./m 3 % No./m 2 %
Minnows 0.04735 23.0 0.12565 31.6 Carp-Goldfish(') 0.00140 0.7 0.00952 2.4 Fallfish 0.00023 0.1 0.00024 0.1 White sucker 0.12339 60.0 0.10324 25.9 Yellow bullhead 0.01843 9.0 0.00904 2.3 Banded killifish - - 0.00048 0.1 Rock bass - - 0.00253 0.6 Lepomis sunfish 0.01283 6.2 0.14686 36.9 Smallmouth bass - - 0.00024 0.1 Tessellated darter 0.00210 1.0 0.00012 -
Total 0.20573 0.39792 (1) All fish in the carp-goldfish category were identified as carp in 1974; most were probably carp in 1973.
LGS EROL TABLE 2.2-75 MEAN DAILY DRIFT DENSITY (No./m 3 ) FOR SELECTED LARVAL FISH COLLECTED FROM EAST BRANCH PERKIOMEN CREEK AT E2650. 1973 AND 1974 1973 Taxa 17 Apr 01 May 15 May 04 Jun 26 Jun 09 Jul 23 Jul 06 Aug 23 Aug 04 Sep Minnows - 0.008 0.017 0.082 0.025 0.031 0.120 0.287 0.024 -
White Sucker - 0.353 0.289 0.030 - - .. -
Yellow Bullhead - - - 0.075 0.034 0.029 - -
Lepomis sunfish .... 0.001 e 0.220 0.004 Tessellated darter - 0.010 ' ......
1974 Taxa 02May 08 May 15 May 20 May 30 May 05 Jun 11 Jun 19 Jun 27 Jun 08 Jul 16 Jul 24 Jul 29 Jul 06 Aug 13 Aug 22 Aug 27 Aug Minnows - 0.002 0.042 0.449 0.184 0.052 0.135 0.159 5.372 0.039 0.015 0.111 0.120 0.094 0.220 0.052 0.081 Carp 0.006 0.009 - 0.420 0.001 - - - - 0.002 0.011 - 0.007 Com on shiner - - . 0.007 - - 0.010 - 0.012 - -
SpottalIshiner .. - 0.001 - 0.028 -.........
White sucker 0.230 1.200 0.106 0.107 0.022 0.021 - -. . . ...
Yellow bullhead - - - W - - 0.114 0.206 0.018 0.015 .....
Rock bass - - - 0.003 ... . ... 0.072 0.009 .-..
Lepomis sunfish . . ..- 0.388 2.169 0.002 0.037 0.092 - 0.420 0.095 0.067 0.001 0.003 -
Tessellated darter - - 0.002 . . . . . ..
LGS EROL Page I of 2 TABLE 2.2-76 MEANCATCH-PER-UNIT-EFFORT (C/F) AND RELATIVE ABUNDANCE OF FISH SPECIES COLLECTED BY SEINE FROM EAST BRANCH PERKIOMEN CREEK IN 1975 AND1976 1975 1976 1975 1976 1975 1976 1975 1976 1975 1976 E36690 E36690 E32170 E32170 E29810 E29810 E26630 E26630 E22980 E22980 Species C/F % C/F % C/F % C/F % C/F % C/F % C/F % C/F C/F % C/F Redfin pickerel 0.74 1.6 0.47 1.4 0.19 0.17 0.1 Goldfish - 0.31 0.2 Carp Cutlips minnow - - - - - 0.32 0.1 0.66 0.2 0.71 0.3 0.53 0.3 Golden shiner 0.23 0.5 4.19 13.0 1.36 0.1 5.24 0.7 0.98 0.2 1.50 0.3 3.32 1.3 1.96 0.5 1.73 0.7 11.85 6.2 Comely shiner 4.24 9.0 1.74 5.4 79.84 7.2 8.84 1.2 12.26 2.5 4.59 0.B 12.76 4.8 2.65 0.6 1.04 0.4 0.46 0.2 Satinfin shiner 0.1
- - - - 1.16 0.1 - - 0.40 0.1 Bridle shiner Common shiner 3.77 8.0 3.37 10.4 15.47 1.4 65.56 9.1 49.97 10.3 30.64 5.6 14.01 5.3 9.61 2.3 2.06 0.90 1.94 1.0 Spottail shiner 0.08 0.2 - - 2.16 0.2 7.36 1.0 2.05 0.4 9.64 1.8 0.89 0.3 0.85 0.2 0.11 Swallowtail shiner 0.49 1.0 0.46 1.4 72.74 6.6 69.17 9.6 39.58 B.2 14.52 2.6 10.83 4.1 14.03 3.3 4.41 1.9 2.92 1.5 Spotfin shiner 28.14 59.7 1.43 4.4 775.43 70.4 238.42 33.2 329.97 68.3 224.41 40.8 194.98 73.9 154.80 36.5 203.25 86.1 64.49 33.9 Bluntnose minnow 0.46 1.0 3.13 9.7 71.01 6.4 141.18 19.7 8.92 1.8 39.30 7.1 5.10 1.9 6.17 1.5 4.88 2.1 1.60 0.8 Blacknose dace - - - - 1.09 0.1 13.50 1.9 1.86 0.4 42.35 7.7 5.05 1.9 41.79 9.9 2.07 0.9 2.36 1.2 Longnose dace 0.45 0.2 0.09 -
Creek chub 3.58 0.8 Fallfish Minnow hybrid "- -- 0.17 White sucker 1.17 2.5 0.79 2.4 11.93 1.1 13.55 1.9 4.39 0.9 78.14 14.2 0.40 0.2 6.38 1.5 0.57 0.2 5.10 2.7 Creek chubsucker 0.49 1.0 1.13 3.5 0.39 0.0 0.44 0.1 0.20 - - - - - -
Yellow bullhead - - - - 0.13 0.0 0.67 0.1 - - 1.69 0.3 - - 0.24 0.1 - - 0.36 0.2 Brown bullhead -S 0.19 0.6 - - 0.44 0.1 - - - - - - - - - 0.15 0.1 Margined madtom Banded killfish - - - - 37.28 3.4 38.95 5.4 10.13 2.1 27.52 5.0 4.07 1.5 47.05 11.1 9.68 4.1 91.05 47.8 Redbreast sunfish 1.00 2.1 0.80 2.5 7.82 0.7 24.61 3.4 3.79 0.8 9.27 1.7 1.11 0.4 0.41 0.1 0.22 0.1 0.33 0.2 Green sunfish 0.53 1.1 5.89 18.2 0.11 0.0 11.21 1.6 - - 0.93 0.2 0.88 0.3 10.83 2.6 2.47 1.0 5.01 2.6 Pumpkinseed 0.67 1.4 1.21 3.7 0.91 0.1 4.03 0.6 0.22 - - - 1.18 0.4 13.38 3.2 0.19 0.1 1.12 0.6 Bluegill 1.06 2.3 0.18 0.5 1.00 0.1 5.50 0.8 1.46 0.3 0.19 - 0.13 0.1 4.05 1.0 0.33 0.1 0.50 0.3 Lepomis hybrid 1.60 3.4 5.13 15.9 0.23 0.0 2.15 0.3 - - - 0.20 0.1 1.22 0.3 0.79 0.3 0.30 0.2 Small bass - - 1.00 0.1 .22 - 0.51 - - 0.2 0.12 Largemouth bass 0.43 0.9 0.09 0.3 0.93 0.1 - - 0.51 0.1 - 0.44 0.2 1.41 0.3 0.11 -
Tessellated darter 2.04 4.3 2.15 6.6 19.63 1.8 66.27 9.2 16.15 3.3 65.21 11.9 8.04 3.0 102.49 24.26 1.07 0.5
0 LGS EROL Page 2 of 2 TABLE 2.2-76 (Cont'd) 1975 1976 1975 1976 1975 1976 1975 1976 Years E12440 E12440 E5475 E5475 E1890 E1890 Mean Mean Mean Species C/F % C/F % C/F % C/F % C/F 7 C/F % C/F % C/F % C/F %
Redfin pickerel . . .. 0.11 - 0.08 - 0.9 -
Goldfi sh .- - 0.04 - .2 -
Carp - - 0.08 - - - - - 0.09 0.1 - - 0.1 - 0.01 - 0.1 Cutlips minnow 2.31 1.4 6.11 2.7 1.56 0.6 1.45 0.1 1 11 0.8 1.73 2.0 0.76 0.2 1.33 0.4 1.04 0.3 Golden shiner 0.05 - 0.45 0.2 - - 0.12 0.1 - - - - 0.97 0.3 3.15 1.0 2.06 0.6 Comely shiner 25.95 15.7 12.28 5.3 4.96 1.9 2.06 1.4 4.07 3.1 1.31 1.6 18.30 5.4 4.27 1.4 11.29 3.5 Satinfin shiner 14.85 9.0 26.76 11.6 67.33 26.1 22.83 15.5 23.90 18.1 13.91 16.5 13.41 4.0 8.09 2.7 10.75 3.4 Bridle shiner - - - - - - - - - - - - 0.20 0.1 - - 0.10 -
Common shiner 8.28 5.0 15.02 6.5 18.50 7.2 13.67 9.3 5.35 4.1 4.46 5.3 14.80 4.4 18.22 6.1 16.51 5.2 Spottail shiner 0.18 0.1 0.85 0.4 0.41 0.2 0.85 0.6 0.11 0.1 1.04 1.2 0.76 0.2 2.61 0.9 1.68 0.5 Swallowtail shiner 2.11 1.3 1.33 0.6 2.63 1.0 2 05 1.4 0.35 0.3 0.09 0.1 16.83 5.0 13.23 4.4 15.03 4.7 Spotfin shiner 96.00 58.1 105.32 45.7 148.45 57.6 62.60 42.5 78.94 59.8 23.70 28.1 234.24 69.1 110.76 36.9 172.50 53.9 Bluntnose minnow 1.76 1.1 2.89 1.3 5.47 2.1 0.80 0.5 0.28 0.2 0.46 0.5 12.37 .3.6 24.71 8.2 18.54 5.8 Blacknose dace 1.33 0.8 10.11 4.4 2.15 0.8 4.90 3.3 0.90 0.7 2.36 2.8 1.83 0.5 14.86 4.9 8.34 2.6 Longnose dace 3.25 2.0 9.21 4.0 0.74 0.3 7.34 5.0 0.90 0.7 4.00 4.7 0.68 0.2 2.61 0.9 1.64 0.5 Creek chub -. - - - - - - - - - - - - 0.45 0.2 0.23 0.1 Fallfish - - - 0.08 0.1 - - 0.1 - - - 0.01 -
Minnow hybrid - - - - - - - - 0.02 - 0.01 -
White sucker - - 13.90 6.0 15.58 10.6 10.57 8.0 24.45 28.9 3.66 1.1 1r.98 6.6 11.82 3.7 Creek chubsucker - - - - - - - - - - 0.13 - 0.19 0.1 0.16 0.1 Yellow bullhead 0.06 - 0.29 0.1 0.49 0.3 - - 22 0.3 0.02 - 0.50 0.2 0.26 0.1 Brown bullhead - - - - - - - - - - - - 0.10 - 0.05 -
Margined madtom - - - 0.08 0.1 0.08 0.1 - - 0.1 - 0.1 - 0.01 -
Banded killfish 6.68 4.0 9.25 4.0 3.70 1.4 2.87 2.0 4.41 3.3 0.73 0.9 9.61 2.8 27.52 9.2 18.56 5.8 Redbreast sunfish 0.57 0.3 1.49 0.6 0.69 0.3 2.50 1.7 0.55 0.4 3.79 4.5 1.98 0.6 5.46 1.8 3.72 1.2 Green sunfish 0.77 0.5 4.06 1.8 0.50 0.2 1.49 1.0 0.20 0.2 0.77 0.9 0.68 0.2 5.01 1.7 2.85 0.9 Pumpkinseed 0.06 - 3.65 1.6 - - 0.63 0.4 - - - - 0.40 0.1 3.02 1.0 1.71 0.5 Bluegill 0.12 0.1 4.50 2.0 0.08 - 0.17 0.1 - - - 0.52 0.2 1.91 0.6 1.21 0.4 Lepomis hybrid 0.12 0.1 0.34 0.1 - - 0.17 0.1 - - - 0.35 0.1 1.11 0.4 0.73 0.2 Small bass 0.13 0.1 - - - - 0.24 0.2 0.19 0.1 1.27 1.5 0.18 0.1 0.23 0.1 0.21 0.1 Largemouth bass - - 0.31 0.1 - - - - - - - - 0.30 0.1 0.23 0.1 0.26 0.1 Tessellated darter 0.52 0.3 2.45 1.1 0.48 0.2 4.32 2.9 - - 0.22 0.3 6.04 1.8 30.75 10.2 18.39 5.8
LGS ERO0 TABLE 2.2-77 RELATIVE ABUNDANCE (IN) ANr BIOMASS (5W) OF FISHES COLLECTED BY ELECTROFISHING FRCM La IC SITES#
PAST BRANCH PERKICHEN CREEK, 1973 AND 1975
- E36020 E305,40 E22240 1973 .1975 1973 1975 1973 1975 LmL. Li L i Li 1-k L L1 % I. JLA Redfin pickerel 3.0 3.1 7.0 6.1 0.1 1.2 0.6 0.9 <0.1 <0.1 0.0 0.0 Chain pickerel 0.0 0.0 0.6 9.6 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 Goldfish 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 1.3 4.1 0.2 0.8 Carp 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.2 1.8 <0.1 0.5 Carp x qoldfish hybrid 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 Golden shiner 2.0 0.9 0.0 0.0 1.9 0.8 1.6 0.7 0.3 0.1 0.1 <0.1 White sucker 17.54 36.7 14.6 39.5 24.6 45.1 20.7 41.8 51.6 72.6 33.3 66.6 Creek chubsucker 5.0 6.6 3.9 3.54 0.1 0.7 2.2 2.8 0.2 0.2 0.1 0.2 White catfish 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 Yellow bullhead 10.3 3.5 5.8 6.5 5.8 10.6 25.5 11.7 6.5 5.7 11.4 11.7 Brown bullhead 1.6 2.2 2.1 1.3 2.4 -4.6 0.8 3.7 1.6 1.7 2.0 5.3 Marqined madtom 0.0 0.0 0.0 0.0 0.0 0.0 <0.1 (0. 1 0.0 0.0 0.0 0.0 Rock Lass 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 Redbreast sunfish 13.3 8.0 12.4 7.4 33.1 21.4 22.2 20.9 0.7 11.3 3.3 2.0 Green sunfish 12.8 18.6 12.1 5.6 13.9 7.3 6.2 5.1 31.6 11.0 43.7 11.5 Pumpkinseed 13.8 7.0 11.1 5.3 8.0 3.9 3.1 1.9 2.5 1.5 3.6 0.8 Blueqill 1.9 0.8 5.3 2.1 3.2 0.7 10.4 3.7 1.2 0.1 0.4 0.1 Leomio hybrid 14.8 10.5 19.4 10.5 2.9 1.6 2.6 2.3 1.2 0.8 1.2 0.3 Smallmoutb bass 1.2 0.4 0.0 0.0 1.3 1.2 0.7 1.7 <0.1 <0.1 0.2 0.1 Larqemouth bass 2.7 1.4 5.8 2.7 1.5 0.9 3.5 2.8 0.2 <0.1 0.2 <0.1 E120540 0 Sites Combined Years 1973 1975 1973 1975 1973 1975 Combin g LiD LiW L1 L.T .L2 %LW S JLi JL LJAW LX Li Redfin pickerel 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.5 0.0 0.7 0.5 0.6 0.5 Chain pickerel 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 (0.1 0.5 (0. 1 0.3 Goldfish 0.6 1.8 0.3 3.5 5.0 4.6 0.7 2.1 1.2 3.0 0.2 1.3 0.6 2.1 Carp 0.0 0.0 0.1 1.4 0.1 31.8 54.4 35.8 0.5 11.4 0.7 11.4 0.6 11.4 Carp x qoldfish hybrid 0.0 0.0 0.0 0.0 0.0 0.0 0.1 0.6 0.0 0.0 <0.1 0.6 (0. 1 0.1 Golden shiner 0.0 0.0 0.0 0.0 0.0 0.0 0.1 0.1 0.7 0.2 0.5 0.1 0.6 0.1 White sucker 27.0 54.6 14.3 27.1 13.4 29.3 6.8 23.9 32.1 48.7 20.1 44.3 25.1 46.3 Creek chubsucker 0.0 0.0 0.0 0.0 0.1 0.1 0.1 0.1 0.5 0.7 0.9 0.7 0.9 0.7 White catfish 0.1 0.1 0.0 0.0 0.0 0.0 0.0 0.0 <0. 1 <0. 1 0.0 0.0 <0.1 <0.1 Yellow bullhead 38.5 254.4 37.6 34.2 22.6 15.1 13.2 10.1 16.0 11.9 21.2 13.2 19.0 12.6 Brown bullhead 0.1 0.6 0.0 0.8 0.6 0.4 0.7 1.3 1.3 1.6 1.0 3.1 1.2 2.4 Marqined madtom 0.0 0.0 0.4 0.2 7.7 0.7 7.5 0.3 1.0 0.2 1.2 0.1 1.1 0.2 Rock bass 0.0 0.0 0.0 0.0 2.9 1.5 1.1 0.7 0.4 0.5 0.2 0.2 0.3 0.3 Redbreast sunfish 7.5 4.4 10.1 15.54 28.7 10.6 37.9 15.0 13.4 7.9 15.8 10.6 14.8 9.4 Green sunfish 8.3 0.9 12.8 1.6 21.4 7.8 24.3 7.5 23.1 7.6 24.5 12.4 33.5 15.2 Pumpkinseed 0.7 0.7 1.8 0.8 0.7 0.2 1.9 0.8 4.6 1.7 3.3 1.2 3.8 1.4 Blueqill 0.5 <0.1 0.0 0.0 0.4 (0. 1 2.5 0.6 1.4 0.2 3.7 0.9 2.7 0.6 Lepomi hybrid 0.2 0.2 0.9 0.3 0.0 0.0 0.7 0.54 2.7 1.3 2.7 1.2 2.7 1.2 Smallmouth bass 0.3 0.1 0.9 1.2 6.5 54.5 8.9 6.6 1.3 1.8 1.8 2.5 1.6 2.2 Larqemouth bass 0.1 1.0 0.1 0.1 0.1 0.1 0.8 0.1 0.7 0.54 1.5 0.6 1.2 0.5
LGS EROL TABLE 2.2-78 RELATIVE ABUNDANCE (% TOTAL CATCH) OF ALL SPECIES COLLECTED BY ELECTROFISHING FROM FRETZ (15500)
AND WAWA (E5650) RESERVOIRS, EAST BRANCH PERKIOMEN CREEK IN 1974 AND 1975.
15500 5650 1974 1975 1974 1975 Total Species % % % % %
American eel 0.1 - - - 0.01 Redfin pickerel - - - 0.01 Goldfish 5.5 1.0 1.1 0.3 1.87 Carp 0.6 1.0 2.4 3.0 1.69 Golden shiner 1.9 0.5 0.1 0.1 0.60 Minnow hybrid 0.1 - 0.4 0.1 0.14 White sucker 23.1 13.8 16.2 6.9 14.97 Creek chubsucker 0.6 0.1 0.1 - 0.22 White catfish - - 0.1 - 0.01 Yellow bullhead 1.4 6.6 18.5 18.9 11.09 Brown bullhead 3.8 5.1 1.8 2.1 3.33 Redbreast sunfish 0.7 3.5 8.9 20.7 7.94 Green sunfish 31.3 28.6 38.3 36.6 33.34 Pumpkinseed 21.8 15 .4 6.7 7.7 12.97 Bluegill 1.4 19.0 0.1 0.6 6.41 Lepomis hybrid 4.5 3.3 4.2 2.5 3.61 Smallmouth bass 0.9 0.6 0.3 0.2 0.53 Largemouth bass 2.3 1.4 0.7 0.5 1.24 Yellow perch 0.1 - - - 0.01
IG S EROL TAELE 2. 2-79 CRITERIA FOR DETERMINATION OF IMPCRTANT FISHES CF EASH BRANCH PERKIOMEN CREEK IMPORTANCE LINK TO PLANT (DIVERSIONj Altered Common Name Recre ation al Ecological Abundant Habitat Redfin pickerel( 1) x X Satinfin shinerC2) x X x Common shiner( 2 ) X X X Spotfin shiner(2) x X x White sucker( 1 )( 3 ) X X x x Yellow bullbead(') X X X X Redbreast sunfish(l ) (3) X x x x Green sunfish(1)(3) x x x Pumpkinseed( 1 ) X X X Smallmouth bass(') X x X Tessellated darter(2) x x x
(')Species sampled by large fish population estimate program.
(2 )Species sampled by seine program.
( 3 )Species sampled by age and qrowth program.
LGS EROI TABLE 2.2-80 POPULATION ESTIMATESC() AND ESTIMATED BICMASS(2) CF SELECTED SPECIES COLLECTED BY ELECTROFISHING FROM LOTIC SITES, EAST BRANCH PERKIONEN CREEK, 1973 AND 1975 E36020 E30540 E22240 E12040 - E1550 Sites Ccrtined SDecies Year N/500L Wt/50f No/500m Wt/5 NO/500m Wt/500 NoS00i 3 WtjS00 IN Or y/500km Nc/500w Vt/5s0o Redfin pickerel 1973 36 1.05 13 0.71 1 0.03 0 0.00 0 0.00 9 0.36 1975 62 1.84 21 0.71 0 0.00 0 0.00 0 0.00 17 0.51 White sucker 1973 185 12.65 390 25.91 1661 100.86 586 35.40 203 47.54 605 44.47 1975 130 11.81 676 31.84 1202 37.54 457 15. 19 162 48.31 525 48.94 Yellow bullhead 1973 110 1.20 91 6.07 208 7.85 833 15.82 343 28.48 317 11.88 1975 52 1.95 835 8.89 413 10.94 1199 19.16 315 20.51 563 12.29 Redbreast sunfish 1973 142 2.76 524 12.20 23 0.41 161 2.83 435 20.09 257 7.67 1975 111 2.22 725 15.80 118 4.21 321 8.63 907 30.27 436 12.24 Green sunfish 1973 136 6.48 220 4.20 1018 15.34 530 7.82 125 1.76 406 7.12 1975 108 1.68 202 3.84 1586 23.84 1069 8.53 307 3.17 654 8.21 Pumpkinseed 1973 147 2.43 126 2.22 112 2.14 16 0.02 12 0.46 83 1.45 1975 99 1.57 100 1.47 129 1.57 57 0.42 47 1.57 86 1.32 Smallmouth bass 1973 13 0.13 20 0.68 1 0.02 6 0.08 98 8.56 28 1.89 1975 0 0.00 24 1.31 7 0.29 30 0.69 213 13.43 55 3.14 C() Number per 500 meters of stream lenqth.
(2) Weiqht in kiloqrams per 500 meters of stream lenqth.
LGS TROL TAFIE 2.2-81 POPULATION ESTIMATES (ISo.) AND ESTIMATED BICMASS (Wt.) OF SELECTED SPECIES COLLECTED BY ELECTROFISHING FROM LENTIC SITES, EAST BRANCH PERKICHEN CREEK, IN 1974 and 1975 E15500 E5650 Sites :cwbined Species Year Ut. (kq)
- (fkal 1ki-ka Wt,0m) No Redfin pickerel 1974 0 - 0 1975 1 - 0 1 White sucker 1 974 1119 - 687 - 1836 1975 576 98.53 654 122.29 1230 220.82 Yellow bullhead 1974 64 - 789 - 853 1975 539 47.72 1433 101.68 1972 152.40 Redbreast sunfish 19741 11 - 230 - 241 1975 113 2.95 827 23.52 940 26.47 Green sunfish 1974 1107 - 1180 - 2287 1975 847 20.96 869 25.50 1716 46.46 Puwpkinseed 1974 931 - 160 - 1091 1975 540 20.42 247 7.15 787 27.57 Smallmouth bass 1974 22 - 7 - 29 1975 14- 6 - 20
LGS ERCL TABLE 2.2-82 IENGSH-WEIGHT RELATIONSHIPS(l) OF SELECTED SPECIES COLLECTEE BY SEINE FROM EAST E!ANCH PERKIOMEN CREEK IN 1975 and 1976 Sgecies Site/Year a b Common shiner E36690 -12.93 3.40 E32170 -12.63 3.33 E29810 -11.94 3.17 E26630 -12.76 3.38 E22980 -11.94 3.18 E12440 -12.37 3.27 E5475 -12.61 3.33 E1890 -12.31 3.25 1975 -12.67 3.34 1976 -12.16 3.23 Spotfin shiner E36690 -11.98 3.13 E32170 -12.14 3.17 E29810 -12.29 3.21 E26630 -12.31 3.22 E22980 -12.51 3.28 E12440 -11.82 3.09 E5475 -12.27 3.21 E1890 -11.97 3.12 1975 -12.28 3.20 1976 -12.00 3.14 In w = a+b In L
LGS EROL TABLE 2.2-83 LENGTH-WEIGHT RELATIONSHIPS(1) OF SELECTED SPECIES COLLECTED BY ELECTROFISHING FFOM LOTIC SITES, EAST BRANCH PERKIOMEN CREEK, IN 1973 AND 1975.
1973 1975 species Site a b a -b White sucker E36020 -12.76 3.27 E30540 -11.59 3.05 E22240 -11.47 3.03 E12040 -10.86 2.92 E1550 -11.37 3.02 Redbreast sunfish E36020 -11.92 3.24 -10.81 3.01 E30540 -11.05 3.06 -10.77 3.01 F22240 -10.29 2.92 -12.20 3.33 E12040 -11.70 3.20 -11.14 3.08 E1550 -10.98 3.05 -11.00 3.06 Green sunfish E36020 -11.01 3.05 -11.68 3.21 E30540 -12.81 3.42 -11.40 3.14 E22240 -11.40 3.12 -11.28 3.12 E12040 -13.29 3.53 -11.95 3.25 E1550 -12.20 3.30 -11.11 3.08 (I) ln W = a+b ln L
0 I:GS EICL I .EIE 2.2-84 MEAN CALCULATED LENGTHS AT ANNULUS FOP FEDFIN PICKEREL COLLECTED AT FIVE SITES ON THE EAST BRANCE PERKICMEN CREEK IN 1973 AND 1975 Mean Calculated Length (Mm FL) at Annulus No. of Age-Group Fis_ I II III - V V I 12 126 ....
II 6 117 170 - - -
III 3 132 184 210 - -
IV 2 132 178 201 234 V 1 94 149 178 205 258 Total 24 24 12 6 3 1 Grand Average lenqth 124 173 202 224 258 Increment 124 49 29 22 34
% Total Growth 48.1 19.0 11.2 8.5 13.2
-GS EPCI.
IAELE 2.2-85 MEAN CALCULATED LENGTHS AT ANNULUS FOP WHITE SUCKER COLLECTED BY ELECTRCFISHING UPSTREAM AND DOWNSTREAM CF SELLERSVILLE, EAST BRANCH PERXIOMEN CREEK, IN 1973 Mean Calculated Lenath 1mm FLI at Ann"I1 ti _Q Mean Calculated Lenatb (mm FLI at J
No. of Agie-G roup Year-Class Lccaticn Fish UI III IV I 1973 Upstream 7 63 Downstream 24 95 II 1971 Urstreav 19 79 143 Downstream 26 91 158 III 1970 Upstream 22 78 133 1914 Downstream 28 81 139 197 IV 1969 Upstream 6 74 118 177 213 Downstream 6 76 136 195 244 Total No. Fisb Upstrear 54 54 47 28 6 Downstream 84 84 60 34 6 Weiqbted Mean F1 Upstream 76 135 190 213 Downstream 88 147 197 244 Increment Upstream 76 59 55 23 Downstream 88 59 50 47
% Total Growth Upstrear 35.7 27.7 25.8 10.8 Downstream 36.1 24.2 20.5 19.2
I.GS ERCL
'TAELE 2.2-86 MEAN CALCULATED LENGTHS AT ANNULUS FOR PEDBREAST SUNFISH COLLECTED BY ELECTROFISHING FROM LCTIC SITES, EAST BRANCH PERKICMEN CREEK, IN 1973 AND 1975 Weiqhted Mean length (vim FL) at Annulu No. of Site Fish Year I II III IV E36020 1973 84 32 66 94 118 143 1975 27 23 58 90 E30540 1973 118 34 65 74 116 138 1 975 54 32 64 93 114 E22240 1973 10 30 70 1975 24 33 89 104 E12040 1973 79 37 86 122 148 166 1975 46 31 80 119 E1550 1973 90 41 94 129 1975 55 33 85 133
IGS EFCL
'IAEIE 2.2-87 MEAN CALCULATED LENGTHS AT ANNULUS FOV GREEN SUNFISH CCLLECTED BY ELECTROFISHING FRCM LOTIC SITES, EAST BRANCH PERKIOMEN CREEK, IN 1973 AND 1975 1 eiqbted Mean LenQth (mm FL)..at Annulus No. of Site Year Fish I II III IV E36020 1973 87 38- 76 108 138 1975 35 28 69 - -
E305[0 1973 79 38 75 106 1975 37 40 80 -
E22240 1973 103 36 77 111 1975 47 33 75 1l3 -
E12040 1973 149 37 77 112 133 1975 30 35 71 108 -
E1550 1973 62 37 77 118 1975 36 32 78 107
LGS EROL TABLE 2.2-88 1976 TOTAL WHEAT PRODUCTION WITHIN 5 MILES OF LGS--
SUMMARY
IN ACRES BY SECTOR AND DISTANCE Distance in Miles Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 4 7 0 11 NNE 10 0 0 0 26 36 NE 0 0 0 0 19 19 ENE 0 0 105 50 0 155 E 0 0 35 0 22 57 ESE 0 0 0 58 10 68 SE 0 0 0 0 105 105 SSE 0 0 6 30 0 36 S 0 0 0 57 17 74 SSW 0 20 0 26 14 60 SW 0 0 25 0 10 35 WSW 0 10 22 0 0 32 W 0 0 30 4 0 34 WNW 0 0 0 0 0 0 NW 0 0 0 0 0 0 NNW 0 0 0 0 5 5 Total 10 30 227 232 228 727
LGS EROL TABLE 2.2-89 1976 TOTAL GRAIN CORN PRODUCTION WITHIN 5 MILES OF LGS--
SUMMARY
IN ACRES BY SECTOR AND DISTANCE Distance in Miles Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 14 36 0 40 NNE 40 0 0 0 65 105 NE 50 0 11 0 60 121 ENE 0 0 148 146 50 344 E 0 0 90 0 51 141 ESE 5 0 0 200 60 265 SE 0 0 0 0 220 220 SSE 0 0 7 250 297 554 S 0 0 10 357 130 497 SSW 15 50 19 125 115 324 SW 0 50 170 31 20 271 WSW 0 35 96 0 140 271 W 0 0 35 5 0 40 WNW 0 0 0 0 0 0 NE 0 0 0. 0 0 0 NNW 0 0 0 0 15 15 Total 110 135 600 1150 1223 3218
LGS EROL TABLE 2.2-90 1976 TOTAL CORN (SILAGE) PRODUCTION WITHIN 5 MILES OF LGS--
SUMMARY
IN ACRES BY SECTOR AND DISTANCE.
Distance in Miles Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 0 0 0 0 NNE 0 0 0 0 0 0 NE 0 0 0 0 0 0 ENE 0 0 10 130 50 190 E 0 0 35 0 22 57 ESE 0 0 0 90 16 106 SE 0 0 0 0 90 90 SSE 0 0 8 40 80 128 S 0 0 4 67 25 96 SSW 0 35 6 48 16 105 SW 0 70 205 11 0 286 WSW 0 35 60 0 75 170 W 0 0 50 0 0 50 WNW 0 0 0 0 0 0 NW 0 0 0 0 0 0 NNW 0 0 0 0 35 35 Total 0 140 378 386 409 1313
LGS EROL TABLE 2.2-91 1976 TOTAL ALFALFA, TIMOTHY AND CLOVER) WITHIN 5 MILES OF LGS--
SUMMARY
IN ACRES BY SECTOR AND DISTANCE Distance in Miles Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 17 35 0 52 NNE 0 0 0 0 40 40 NE 0 0 34 0 83 117 ENE 0 0 75 70 32 177 E 0 0 0 0 12 12 ESE 0 0 0 0 30 30 SE 0 0 0 0 25 25 SSE 0 0 18 75 100 193 S 0 0 10 54 101 165 SSW 10 15 0 77 61 163 SW 0 45 140 6 30 221 WSW 0 0 63 0 125 188 W 0 0 60 30 0 90 WNW 0 0 0 0 0 0 NW 0 0 0 0 30 30 NNW 0 0 0 0 51 51 Total 10 60 417 347 720 1554
LGS EROL TABLE 2.2-92 1976 TOTAL (ALL CROPS) PRODUCTION WITHIN 5 MILES OF LGS--
SUMMARY
IN ACRES BY SECTOR AND DISTANCE Distance in Miles Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 51 78 0 129 NNE 58 0 0 0 217 275 NE 80 0 50 0 284 414 ENE 0 0 528 433 152 1113 E 0 0 250 0 157 407 ESE 5 0 0 538 132 675 SE 0 0 0 0 552 552 SSE 0 0 42 515 610 1167 S 0 0 29 821.5 331 1181.5 SSW 25 178 62 380 274 919 SW 0 165 720 66 70 1021 WSW 0 155 319 0 390 864 W 0 0 191 47 0 238 WNW 0 0 0 0 0 0 NW 0 0 0 0 40 40 NNW 0 0 0 0 142 142 Total 168 498 2242 2878.5 3351 9137.5
LGS EROL TABLE 2.2-93 1976 TOTAL COW POPULATION WITHIN 5 MILES OF LGS BY SECTOR AND DISTANCE Distance in Miles Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 0 0 0 0 NNE 0 0 0 0 0 0 NE 0 0 16 0 0 16 ENE 0 0 30 125 60 215 E 0 0 40 0 43 83 ESE 0 0 21 119 34 174 SE 0 0 0 0 137 137 SSE 0 0 26 114 50 190 S 0 0 12 213 45 270 SSW 0 53 23 96 58 230 SW 0 70 245 38 0 353 WSW 0 87 90 0 105 262 W 0 0 35 0 0 35 WNW 0 0 0 0 0 0 NW 0 0 0 0 0 0 NNW 0 0 0 0 0 0 Total 0 190 538 705 532 1965
LGS EROL TABLE 2.2-94 1976 TOTAL GOAT POPULATION WITHIN 5 MILES OF LGS BY SECTOR AND DISTANCE Distance in Miles, Direction 0-1 1-2 2-3 3-4 4-5 0-5 N 0 0 0 0 0 0 NNE 0 0 0 0 2 2 NE 0 0 0 0 0 0 ENE 0 0 0 0 0 0 E 0 0 0 0 0 0 ESE 0 0 2 0 0 2 SE 0 0 0 0 0 0 SSE 0 0 0 0 0 0 s 0 0 0 85 1 86 SSW 0 0 0 0 1 1 Sw 0 0 0 0 0 0 wsw 00 0, 0 0 0 w 0 0 0 0 0 0 WNW 0 0 0 0 0 0 NE 0 0 0 0 0 0 NNW 0 0 0 0 0 0 Total 0 0 2 85 4 91
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT PRINCIPAL PLANT COMMUNITIES FIGURE 2.2-1
MSHROOM PLANTS (MODIFIED FROM JENSEN & SALISBURY; p 742 Ref 2.2-11)
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT HYPOTHETICAL FOOD WEB FIGURE 2.2-2
N MONTGOMERY COUNTY CHESTER COUNTY o - BEI SCALE IN KILOMETERS LIMERICK GENERATING STATION AfREA UNITS 1 AND 2 ENVIRONMENTAL REPORT SCHUYLKILL RIVER, LGS STUDY AREA FIGURE 2.2-3
FLOW z m S700 S75 c C S.
LINFIELO N~ ~ Z G) 180 00 BRIOGE CV,. z ZZ m m A
- MYRIOPHYLLUM EXALDESEENS ha G) se HETERANTHERA DURIA 0 -~POTAIDGETON CRISPUS I2
> -II P.BERCHTOLDII CA Z 0
-4 2
2.53 1.65 1.22 2.04 ..... 19 7 4 I if I I 1975 1.0 I a3 £
~ I -- -- 1976 I *
~
I I
- I if 3
1 I
I 0.8 / I I
I I
I I
/ I I
I I
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I Kn / I I
I I I
/
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0.6 / I I
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I
."A \
m *O )' m .3 U
0.2 zt-z m LAm-5 > -X
> zn C02 -4
700 r-600H 500 --
WI' 200
'1 C
m
-zo Ni NJ 100 0
o -i JUNE JULY AUGUST I -i aomo 9 Mz
30r- 0 1975 -- -
1976 251-CIV W-I~
20-u- J 151- -0 01- - * "N-.0d CD -a cc 16-5F 0' I I I I I I I I I I I I JAN FED NAR APR MAY JUN JUL AUG SEP OCT NOV DEC MONTH 30r-1975---
A 1876 F
S20 1-
-a15 caJC 10I I-5_
III I I I I I I I II 0
$81750 S78900 S78460 S77980 S77240 S77220 S77010 S76840 S76820 S76310 S53 STATION
-0 BY MONTH ALL STATIONS COMBINED.
0 BY STATION ALL MONTHS COMBINED.
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT NUMBER OF FISH SPECIES COLLECTED BY SEINE FROM THE SCHUYLKILL RIVER FIGURE 2.2-7
7000 70 6000 50 r"
eeoe
.I *..w, !
°IoF , =~4 0 _ .. ! ... / N ,.
!q 3000 350"
,ooS -,.,,,...,
-u0 me2 I -- "o0' - qu o .
200 OA 1000 0 410
>- M M ca . .
m 0olno 97 S4 30 m0C I < 31 J AN FEB MiAR APR MiAY JUN JUL AUG SEP OCT NOV DEC
>Z a !,*
> . ,*u 1975 mom mTOTAL NUMBOER97 0- 1975 S=5--
--- . m* PERCENTAGE m a
-. r. - -.. S r- m rl 1*
I &
8000 --. 80 7000 /- 70 6000 s 5000 50
- 0 0 ""
4000 B0 401*0 3000 /...
2000 2.0
-. -4 0197 13000 A 10U Z C./ 0~ 'a olum EIA P A u MA JL 0 U / E C O E 0~ >*
m rz>/ -.
- m~~~ -2z..'
-0zf-01975 m CO) m -40o zPERCENTAGE E 2 mz- 0 -q 98...
~m 1 -.
A I
7000 r-1973 1975 6000 5000 1-o 4000 LAi
&I,,
3000 -
2000 F-1000 I :ii Iv ylv u-u-AGE-GROUP LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT LATE SUMMER AGE STRUCTURE OF BROWN BULLHEAD FIGURE 2.2-10
LEGEND REDBREAST Lu 60
-J..
A- AQUATIC 40 INSECTS 20 M- MOLLUSCA Lu 20 T - TERRESTRIAL 40 ORGANISMS C.3 60 C- CRUSTACEA 80 An- ANNELIDA FALL WINTER PUMPKINSEED 0 - OTHER AQUATIC LLU 60 I ORGANISMS -a 40 20 Lu 20 40 C.3 60 60 FISH COLLECTED FROM THE SCHUYLKILL RIVER (S77240-S75350), 19 JUNE, 1973 THROUGH 11 JUNE, 1974.
0 100O go0ý E-' REDBREAST SUNFISH 87 GREEN SUNFISH 7-PUMPKINSEED 80k-73
,70 m r-
~60 I-56
~50 w 49 r~n40 K
36 CA~ 23 mccm r-201--
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FIGURE 2.2-14
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_ __ _ _ _ _ I _ _
LGS EROL CHAPTER 5 ENVIRONMENTAL EFFECTS OF STATION OPERATION TABLE OF CONTENTS Section Title 5.1 EFFECTS OF OPERATION OF HEAT DISSIPATION SYSTEM 5.1.1 Effluent Limitations and Water Quality Standards 5.1-1.1 Receiving Water Standards 5.1.1.2 Effluent Limitations 5.1.2 Physical Effects 5.1.3 Biological Effects 5.1.3.1 Schuylkill River 5.1.3.1.1 Intake 5.1.3.1.2 Thermal Discharge 5.1.3.2 Perkiomen Creek 5.1.3.2.1 Diversion 5.1.3.2.2 Intake 5.1.3.3 East Branch Perkiomen Creek 5.1.4 Effects of Heat Dissipation Facilities 5.1.4.1 Predicted Climatology of Visible Plume Geometry 5.1.4.1.1 Criteria Used in the Plume Analysis 5.1.4.1.2 Meteorological Input 5.1.4.1.3 Predicted Plume Dimensions 5.1.4.2 Environmental Effects of Natural Draft Cooling Towers 5.1.4.2.1 Visible Plumes 5.1.4.2.2 Fog and Icing 5.1.4.2.3 Cloud Modification 5.1.4.2.4 Precipitation Modifications 5.1.4.2.5 Humidity Changes 5.1.4.2.6 Cooling Tower Drift.
5.1.4.2.7 Environmental Effects of Cooling Tower Blowdown Water 5.1.4.2.8 Cooling Tower Noise 5.1.4.3 Environmental Effects of the Ultimate Heat Sink 5.1.5 References 5.2 RADIOLOGICAL IMPACT FROM ROUTINE, OPERATION 5.2.1 Exposure Pathways 5-i Rev. 15, 08/83
LGS EROL TABLE OF CONTENTS (Cont'd)
Section Title 5.2.1.1 Pathways to Man 5.2.1.2 Pathways to Biota Other than Man 5.2.2 Radioactivity in the Environment 5.2.2.1 Long Term Estimates 5.2.2.1.1 Radioactivity Released to the Atmosphere 5.2.2.1.2 Meteorological Input 5.2.2.1.3 Plume Rise 5.2.2.1.4 Diffusion Model 5.2.2.1.5 Plume Depletion and Deposition 5.2.2.2 Surface Water Models 5.2.2.2.1 Transport Models 5.2.2.2.2 Transit Times 5.2.3 Dose Rate Estimates for Biota Other than Man 5.2.4 Dose Rate Estimates for Man 5.2.4.1 Liquid Pathways 5.2.4.2 Gaseous Pathways 5.2.4.3 Direct Radiation from Facility 5.2.4.4 Annual Population Doses 5.2.5 Annual Radiation Doses 5.2.6 References
- 5. 2A Radiological Dose Model-Liquid Effluents
- 5. 2B Radiological Dose Model-Gaseous Effluent
- 5. 2C 50-Mile Population and Contiguous Population Dose Model 5.3 EFFECTS OF CHEMICAL AND BIOCIDE DISCHARGES 5.3.1 Effects of Discharges, on the Schuylkill River 5.3.1.1 Mixed Discharge Concentrations 5.3.1.2 Comparison to Water Quality Criteria 5.3.1.3 Conditions During Low Flows 5.3.2 Effects of Spray Pond Water Quality 5.3.3 Effects of Cooling Tower Drift on the Surroundings 5.3.4 References 5-ii Rev. 15, 08/83
LGS EROL TABLE OF CONTENTS (Cont'd)
Section Title 5.4 EFFECTS OF SANITARY WASTE DISCHARGES 5.5 EFFECTS OF OPERATION AND MAINTENANCE OF THE TRANSMISSION SYSTEMS 5.6 OTHER EFFECTS 5.6.1 References 5.7 RESOURCES COMMITTED 5.8 DECOMMISSIONING AND DISMANTLING 5.8.1 References 5.9 THE URANIUM CYCLE 5-iii Rev. 15, 08/83
LGS EROL CHAPTER 5 TABLES Table No. Title 5.1-1 Average Thermal Discharge Characteristics During Full Operation 5.1-2 Weekly Schuylkill River Withdrawals During LGS Two Unit Simulated Full Power Operation 5.1-3 Entrainment Loss of Macroinvertebrates at LGS 5.1-4 Predicted Entrainment Loss of Fish Eggs and Larvae During 1975 Spawning Season 5.1-5 Thermal Tolerance of Important Fishes of the Schuylkill River Near LGS 5.1-6 Predicted Seasonal Avoidance Temperature at 95%
Confidence Limits of Important Fish Under Two Conditions of LGS Operation 5.1-7 Predicted Seasonal Preference Temperature and 95%
Confidence Limit of Important Fishes Under Two Conditions of Operation 5.1-8 Weekly Perkiomen Creek Water Withdrawal During LGS Two Unit Simulated Operation 1974-78 5.1-9 Predicted Entrainment Loss of Fish Eggs and Larvae at the Graterford Intake, Perkiomen Creek, During the 1975 and 1976 Spawning Season 5*. 1-10 Distribution of Philadelphia ESMU Upper Air Soundings 5.1-11 Percent Frequency Distributions of Plume Rise 5.1-12 Directional Distribution of Long and Evaporated Plumes 5.1-13 Drift Model Input Parameters by Month 5.1-14 Relative Humidity Distribution (%)
5.1-15 Wind Direction Frequency Distribution (%)
5.1-16 Average Wind Speed by Directional Sector (%)
5iv
LGS EROL CHAPTER 5 TABLES (Cont'd)
Table No. Title 5.1-17 Monthly and Annual Mean Temperatures (OF) at Weather Station No. 1 5.1-18 NaCl Annual Deposition as a Function of the Distance from the Tower 5.1-19 Monthly'NaCl Deposition at Site Boundary 5.1-20 Monthly NaCl Deposition at 1/2 Mile Distance 5.1-21 Monthly NaCl Deposition at 1 Mile Distance 5.1-22 Draft Water Deposited at Site Boundary 5.2-1 Maximum Calculated Radionuclide Concentrations in the Environment from Routing Atmospheric Releases 5.2-2 Maximum Calculated Radionuclide Concentrations in the Environment from Routine Liquid Releases 5.2-3 Calculate Radionuclide Concentration in the Schuylkill River at Drinking Water Intakes Resulting from Routine Liquid Release 5.2-4 Annual X/Q - Uncorrected 5.2-5 Annual X/Q - Corrected for Depletions by Deposition 5.2-6 Annual D/Q 5.2-7 LGS Vent Parameters 5.2-8 Worst Case Dilution Factors and Transit Time 5.2-9 Usage Date for Biota Other than Man 5.2-10 Calculated Exposures to Biota Other than Man 5.2-11 Calculated Maximum Doses from LGS Liquid Radwaste Releases for Each Pathway 5.2-12 Calculated Maximum Annual Doses from LGS Liquid Radwaste Releases to Each Organ from all Pathways 5v
LGS EROL CHAPTER 5 TABLES (Cont'd)
Table No. Title 5.2-13 Calculated Annual Doses for all Real Pathways at the Location of Maximum Offsite Dose to any Organ Resulting from LGS Atmospheric Releases 5.2-14 Direct Radiation Dose 5.2-15 Annual Population Exposure in the Contiguous U.S 5.2-16 50 Mile Annual Population Exposure Resulting from LGS Gaseous Effluents (specific) 5.2-17 50 Mile Annual Population Exposure Resulting from LGS Gaseous Effluents (general) 5.2-18 Comparison of Maximum Individual Doses Resulting from LGS with 10 CFR 50 Appendix I Design Objectives 5.2A-1 Individual Liquid Dose Equations 5.2A-2 Locations for Liquid Effluent Dose Assessment for LGS 5.2A-3 Liquid Pathway Usage and Consumption Rates for LGS 5.2B-1 Annual Average Wind Speed 5.2B-2 Dose Factors for Noble Gases and Daughters for Incremental Lung Dose 5.3-1 Comparison of Schuylkill River Water Quality with Mixed Discharge for December, January, and February of 1975 Through 1978 5.3-2 Comparison of Schuylkill River Water Quality with Mixed Discharge for March, April, and May of 1975 Through 1978 5.3-3 Comparison of Schylkill River Water Quality with Mixed Discharges, for June, July, and August of 1975 through 1978 5.3-4 Comparison of Schuylkill River Water Quality with Mixed Discharge, for September, October, and November of 1975 Through 1978 5vi
LGS EROL CHAPTER 5 TABLES (Cont'd)
Table No. Title 5.3-5 Compilation of Water Quality Criteria for the Reach of the Schuylkill River into which LGS will Discharge 5.3-6 Comparison of Limerick Water Quality Extrema with Published Criteria 5.3-7 Results of Bioassey Determinations on LGS Important Species 5.3-8 Comparison of Schuylkill River Water Quality with Discharge Mixed with One Third of Schuylkill Flow 5.3-9 Predicted Water Quality Concentrations for Q 7-10 Flow of 250 cfs Based on Flow Concentration Relationships Using August Through October Data, 1975 to 1978 5.9-1 Uranium Fuel Cycle Environmental Data FIGURES Figure No. Title 5.1-1 Initial Dilution Area of Diffuser Discharge 5.1-2 Two Cooling Towers 5.1-3 Noise Level Versus Distance 5.2-1 Exposure Pathways to Man 5.2-2 Exposure Pathways to Biota Other Than Man 5.2A-1 Locations at Which Annual Doses to Individuals Resulting from Limerick Liquid Radwaste Releases Were Evaluated 5.6-1 Transmission System Arrangement of Transformers Within the Switchyards 5-vii Rev. 10, 02/83
SECTION 5.1, EFFECTS OF OPERATION OF HEAT DISSIPATION SYSTEM (84 pages)
LGS EROL 5 ENVIRONMENTAL EFFECTS OF STATION OPERATION 5.1 EFFECTS OF OPERATION OF HEAT DISSIPATION SYSTEM This section discusses the thermal effects associated with the heat dissipation system. Chemical water quality effects associated with this system are discussed in Section 5.3.
5.1.1 EFFLUENT LIMITATIONS AND WATER QUALITY STANDARDS Discharges from the Limerick Generating Station are mixed in the Schuylkill River which flows into the Delaware River Estuary.
Pennsylvania is the only state whose waters could be affected by discharges from the station.
5.1.1.1 Receiving Water Standards The waters of the Commonwealth of Pennsylvania are protected by the Department of Environmental Resources (DER) for certain general uses and general water quality criteria are applied to all waters on a statewide basis. The standard water uses protected are warm water fish propagation, fishing, water contact sports, natural area, power generation, and treated waste assimilation, as well as domestic, industrial, livestock, wildlife, and irrigation water supply. The general water criteria control the discharge of substances in concentrations which may be harmful to animal or plant life. Specific substances controlled include, but are not limited to, floating debris, oil, scum and other floating materials, toxic substances, and substances which produce color, tastes, odors, turbidity, or settle to form sludge deposits.
Specific receiving water quality criteria have been established for the Schuylkill River. The specific receiving water quality criteria for the reach of river to which the LGS discharge is made are specified in Ref 5.1-1 as:
- a. pH: Not less than 6.0 and not more than 8.5.
- b. Dissolved Oxygen: Minimum daily average of 5.0 mg/l; no value less than 4.0 mg/l.
- c. Iron: Total iron not more than 1.5 mg/l.
- d. Temperature: Not more than a 50 F rise above ambient temperature or a maximum of 87 0 F, whichever is less; not to be changed by more than 20 F during any 1-hour period.
- e. Dissolved Solids: Not more than 500 mg/l as a monthly average value; not more than 750 mg/l at any time.,
5.1-1
LGS EROL
- f. Bacteria: The fecal coliform density in five consecutive samples shall not exceed a geometric mean of 200/100 ml.
- g. Copper: Not more than 0.10 mg/l.
The DER has not specified a mixing zone or thermal discharge limitations in Water Quality Management Permit No. 671202.
Nevertheless, the DRBC has applied a mixing zone condition for Limerick in the Water Use Approval D-69-210 CP (Final). The DRBC condition states:
"The discharge of the wastewater shall not increase the natural temperature of the receiving waters by more than 50F (above the average daily temperature gradient displayed during the 1961-66 period), nor shall such discharge result in a stream temperature exceeding 870F, except within an assigned heat dissipation area consisting of one-half the stream width and 3500 feet downstream from the discharge point."
5.1.1.2 Effluent Limitations The U.S. Environmental Protection Agency (EPA) has recommended thermal effluent limitations in 40 CFR 423 for steam electric power generating point sources such as Limerick that specify:
"There shall be no discharge of heat from the main condensers except:
- 1) Heat may be discharged in blowdown from recirculated cooling water systems provided the temperature at which the blowdown is discharged does not exceed at any time the lowest temperature of recirculated cooling water prior to the addition of the make-up water.
- 2) Heat may be discharged in blowdown from cooling ponds provided the temperature at which the blowdown is discharged does not exceed at any time the lowest temperature of recirculated cooling water prior to the addition of the make-up water."
Chemical effluent limitations are discussed in Section 5.3.
5.1.2 PHYSICAL EFFECTS Cooling tower blowdown, spray pond overflow, treated radwaste, treated sanitary waste, and holding pond effluent are all mixed together and discharged into the Schuylkill River through the diffuser described in Section 3.4. The cooling tower blowdown will account for more than 99% of the flow rate and heat content
- 5. 1-2
LGS EROL of the total discharge. Therefore cooling tower blowdown is the only heat source considered in the following analysis of thermal effects.
Discharge through the diffuser will cause a rapid dilution of the effluent in the Schuylkill River. For typical river flows it is estimated that the effluent will become fully mixed in that portion of the Schuylkill River which passes over the diffuser.
This estimate is based on the results of MIT laboratory model studies on the performance of submerged diffusers in shallow water (Ref 5.1-2).
The initial mixing zone is the region in which nozzle velocities are dissipated and the effluent is fully mixed with the river flow passing over the diffuser. The estimates of downstream extent of the mixing zones given above are based on methods presented in Reference 5.1-75. For average conditions (river flow rate of 1910 cfs, diffuser flow rate of 26.8 cfs), the initial mixing zone will be about 150 feet wide and 30 feet long (Figure 5.1-1). For a high river flow rate of 9800 cfs (1%
exceedance value), the resulting dilution of the effluent would be much greater and the mixing zone would extend about 150 feet downstream. The areas of these initial mixing zones for average and high river flow conditions are approximately 0.1 and 0.5 acre, respectively. The mixing zone area for river flows lower than average will be less than 0.1 acre.
At river current velocity of 1 foot per second (which is less than the mean velocity for average flow), an organism would pass through the initial mixing zone in about 0.5 and 2.5 minutes for average and high river flow rate conditions, respectively.
Table 5.1-1 gives effluent flow rates, dilution factors, and temperature rises for the discharge plume for monthly cooling tower blowdown temperatures with 50, 5 and 1% probabilities of exceedance. Under average stream flow conditions and all blowdown temperature conditions, even a sudden commencement or cessation of discharge flow would not cause the river temperature outside the small area of initial dilution to be changed by more 0
than 2 F during any one-hour period. Under extreme low flow conditions, a 3-hour gradual commencement or cessation of diischarge would not cause the river temperature to be changed by more than 20 F durin4 any one-hour period. The only set of conditions for which the temperature rise limitation of 50 F is exceeded is for the 1% exceedance blowdown temperature for October and for the 7-day, 10-year low river flow. Even under this unlikely combination of extreme conditions, the computer temperature rise (5.3°F) is only slightly above the limit. It is apparent that the likelihood of effluent temperatures being a constraint on plant operation is very small. The dilution factors presented in Table 5.1-1 also apply to the dilution of chemical constituents in the effluent (Section 5.3).
5.1-3 Rev. 2, 12/81
LGS EROL In the Environmental Report-Construction Permit Stage (Ref.
5.1-3) and the Final Environmental Impact Statement (Ref. 5.1-4),
a constant blowdown of 20 cfs was assumed to mix with one-half the river flow. Since that time, the system design has been finalized. Minor changes have been made to the nozzle design, system controls, and the diffuser location. The blowdown flow rate has been determined to vary between 30 and 32 cfs. One-half to one-third of the river flow will pass over the diffuser. It has been conservatively assumed that the effluent will have become diluted in one-third of the river flow.
5.1.3 BIOLOGICAL EFFECTS The following discussion of the biological effects of the heat dissipation system is based primarily on information gathered by the Applicant's ecological consultant in the Schuylkill River, Perkiomen Creek, and East Branch Perkiomen Creek (Sections 6.1 and 2.2), as well as design and operational parameters presented in the ERCP (PECo, Ref 5.1-3) and FES (USAEC, Ref 5.1-4), and simulated real time plant operating conditions. Chemical effects are discussed in Section 5.3.
General: No rare, threatened, or commercially valuable species were found in 9 years of collecting (1970-1978). Although all three potentially affected streams suffer from past or present anthropogenic activities (Section 2.2.2), all are biologically productive and diverse.
Schuylkill River: Only minor impact is expected on all biotic components (Section 2.2) as a result of intake operation and thermal discharge, due to the low proportion of total flow withdrawn and the small localized increase in temperature, respectively. At present the area near LGS is lightly utilized for sport fishing. However, the river was recently designated Pennsylvania's first scenic river, which probably increases its potential for recreational development. Water quality has been improving and is expected to continue to improve. An American shad restoration program has been initiated by the Pennsylvania Fish Commission. The river near LGS is not of unique importance for the life-sustaining activities of resident aquatic organisms, and the discharge will under no conditions block fish movement past LGS.
Perkiomen Creek: Diversion, by increasing flow and wetted area, should slightly benefit creek biota between the East Branch confluence and intake, especially in low flow years. A relatively large percentage of total flow will be withdrawn by the Graterford intake, but intake design (wedge wire screen) is expected to minimize impingement, and entrainment is expected to have little or no impact on phytoplankton, zooplankton, or macrobenthos. Fish entrainment will be reduced by use and location of the wedge wire screens. The creek near Graterford is not of unique importance for the life-sustaining activities of Rev. 2, 12/81 5.1-4
LGS EROL resident aquatic organisms. Water level fluctuations downstream of the intake will affect, through alternating inundation and exposure, a small area of stream bottom and associated resident biota. There is presently an active sport fishery on Perkiomen Creek.
East Branch Perkiomen Creek: Changes in abundance and d*i'stribution are expected here for some biota in response to diversion. Changes related to flow augmentation (principally through elimination of intermittent flow in the headwaters and improved water quality in the middle and lower reaches) will generally be beneficial to the creek ecosystem through enhancement of community productivity and diversity. The recreational fishery is expected to improve. Diversion may introduce species here and on Perkiomen Creek that have not yet been recorded from these creeks.
5.1.3.1 Schuylkill River 5.1.3.1.1 Intake Operation of the LGS cooling water intake will affect some aquatic biota through impingement and entrainment. Some organisms too large to pass through the 6-mm mesh traveling screens will become impinged and disposed of with the trash. It is assumed that smaller organisms that pass through the intake screens will suffer 100% mortality as a result of extended exposure to temperature differentials and physical and chemical stresses within the cooling system.
For purposes of impact evaluation it is assumed that at the annual average withdrawal rate, approximately 2.6% of river flow will be used at mean flow (50.2 m Is), 9.3% at 7-day, 10-year low flow (7.0 m Is), and 27.2% at lowest recorded flow (2.4 m Is).
Information derived from 316(b) studies conducted at Cromby (CGS, 13 km downstream of LGS, PECo (Ref 5.1-5), Barbadoes (BGS, 40 km downstream, PECo (Ref 5.1-6), and Schuylkill (SGS, 67 km downstream, PECo (Ref 5.1-7) Generating Stations is presented where applicable.
- a. Impingement Large invertebrates and juvenile and adult fish will be impinged. The number of organisms impinged is largely a function of intake location (as related to the variety and distribution of nearby fauna) and design. An intake not located in an area of high macroinvertebrate and fish density, and withdrawing a relatively small volume of water at low velocity, generally has a low potential for deleterious impingement impact (USEPA:p. 19 Ref 5.1-8). Based on these criteria the Schuylkill intake is not likely to impinge large numbers of macroinvertebrates or fish.
5.1-5 Rev. 2, 12/81
LGS EROL Macroinvertebrates: Several important macroinvertebrates (crayfishes, Cambarus bartoni and Orconectes spp.; snails, Goniobasis virginica; and leeches, Erpobdella punctata) are large enough ( 6 mm) to be impinged. However these are benthic dwelling organisms which were never collected in drift samples near LGS (Section 2.2.2.1.6). Thus it is highly unlikely that a significant number of these organisms will be impinged. Crayfish were impinged at CGS, BGS, and SGS, but only one at each station.
Fish: The intake location is not an area of concentrated abundance for any important fishes (Section 2.2.2.1.7), and rare, endangered, or commercially valuable species do not presently inhabit this reach of the Schuylkill. American shad may be restored to the river during the life of the plant (Section 2.2.2.1.7). Striped bass and other migratory species could also be re-established, or in the case of the American eel become more abundant, when fish passages are constructed at downstream dams.
Fish passage facilities have been installed at Fairmount Dam.
Spawning, localized migration, and feeding of resident fishes take place in the general intake location, but the area is not of unique importance for these activities. In addition the area is only lightly utilized for sport fishing (Harmon, Ref 5.1-9).
The following operational and design features will help minimize entrapment and impingement of fishes: (1) the volume of water withdrawn (Section 3.3) will be small relative to total river flow, (2) at average (0.56 m Is) and maximum (0.70 m /s) blowdown, design approach velocities to the screens will be 0.13 and 0.16 m/s, respectively, under low flow (7-day, 10-year) clean screen conditions, (3) the face of the traveling screens will be set nearly flush with the river bank and preceded only by trash racks, so that lateral passage and stream flow may assist fish to escape, and (4) no curtain or skimmer wall (commonly a significant contributor to impingement) will be used.
The differences in elevation of the river bottom, front foot wall, and interior structure floor will create a pool about 1.7 m deep immediately in front of the traveling screens (Figure 3.4-9). This pool may attract and concentrate fish which increases the potential for impingement. Impinged fish that are carried up on the screens will be deposited in a trash receptacle.
Rates of impingement will vary among species. Fishes that migrate or undertake frequent localized movements are generally more susceptible to impingement than sedentary species. The catadromous American eel and anadromous American shad (if restored to the river) are both likely to migrate upriver and downriver past LGS. However, studies at power plants on the nontidal portion of the Delaware River (Lofton, Ref 5.1-10) have indicated that neither juvenile nor adult shad nor eels are frequently impinged from free-flowing waters, and the 316(b) studies at CGS and BGS on the Schuylkill River indicated few eels Rev. 2, 12/81 5.1-6
LGS EROL were impinged. The majority of fish impinged at CGS were brown bullheads and white suckers. Most were collected in spring, probably as a result of localized spawning movements. It is probable that a similar situation will occur at LGS. Goldfish, brown bullheads, and pumpkinseeds exhibited considerable movement near LGS. The redbreast sunfish does not move frequently or far enough to cause serious movement related impingement, but due to its high abundance is likely to be regularly impinged. At CGS and BGS swallowtail shiners and spotfin shiners were infrequently found in impingement collections; banded killifish and tessellated darters were not collected. However it is difficult to determine whether these species actually avoid impingement, or, due to their small size, are entrained.
Fish impingement at LGS is expected to be below that recorded at CGS (11,199 fish impinged per year) and BGS (3319) because of the improved intake design at LGS. LGS intake capacity is only 15%
and 41% of that at CGS and BGS, respectively. LGS design intake average velocity is approximately one-third that at CGS and BGS.
- b. Entrainment Drifting phytoplankton, zooplankton, benthic macroinvertebrates, and fish eggs and larvae will be entrained by the LGS intake. Weekly withdrawal projections summarized in Table 5.1-2 were used to estimate entrainment. It is assumed that all drifting biota, except fish eggs and larvae, are uniformly distributed in the Schuylkill, and that entrainment loss will be proportional to water withdrawn. Fish eggs and larvae were not uniformly distributed in the river near LGS (Section 2.2.2.1.7); and therefore loss of these organisms was estimated from densities within the portion of water withdrawn.
Phytoplankton and Zooplankton: The effects of entrainment on phytoplankton and zooplankton near LGS are expected to be minimal because (1) the proportion of river flow withdrawn will be low, (2) population densities near LGS are known (phytoplankton) or presumed (zooplankton) to be low (Sections 2.2.2.1.2 and 2.2.2.1.5), (3) most phytoplankton in the Schuylkill is dislodged periphyton which continually enters the water column due to scouring action, and (4) both components typically have high reproductive rates.
Macroinvertebrates: Most important macroinvertebrate species rarely drift (Section 2.2.2.1.6). For those that do, only a small proportion of the benthic population drift at any one time (Table 2.2.2.1-14). Furthermore, withdrawal of river flow and subsequent loss of drifting macroinvertebrates will be low (Table 5.1-3). Therefore entrainment of drifting macroinvertebrates is expected to have little impact on either local macroinvertebrate populations or fish which feed on macroinvertebrate drift.
5.1-7 Rev. 2, 12/81
LGS EROL Fish: Important species (Section 2.2.2.1.7) which reproduce in the Schuylkill near LGS either construct nests or broadcast adhesive eggs. As a result, few eggs enter the water column, and based on 1975 and 1976 spawning season data, only a small percentage of such eggs are expected to be withdrawn (Table 5.1-4).
It has been suggested that larval fish drift in streams is an important dispersal mechanism which prevents overcrowding of nursery habitat and enhances larvae survival (Nikolsky: p. 250, Ref 5.1-11; Dovel: p.13, Ref 5.1-12). Because most drifting larvae near LGS are alive entrainment will add to natural mortality. However, neither dispersion nor mortality will be significantly affected due to the relatively low percentage of larvae withdrawn. Consequently, entrainment of eggs and larvae is not expected to seriously alter species composition or density of important species near LGS. In 1975 and 1976, taxa which hypothetically would have suffered the greatest losses under normal station operation were those that drifted in greatest density along the intake shore (Table 5.1-4), but losses incurred during the entire spawning season would not have been of sufficient magnitude to significantly affect adult population numbers.
Some fishes larger than larvae but smaller than the size at which impingement occurs will be entrained. Limited knowledge of the distribution and behavior of juvenile fishes makes evaluation of this potential impact difficult. However, as with entrainment of larvae, the small proportion of river water withdrawn should preclude a significant impact.
5.1.3.1.2 Thermal Discharge The thermal discharge will meet criteria outlined by the Delaware River Basin Commission (Section 5.1.1.1). Estimated monthly average blowdown temperatures can be as much as II.1C above ambient (Table 5.1-1). However, the diffuser (Section 5.1.2) will promote rapid mixing, and only a slight increase ( 1C) above ambient will occur after full mixing with one-third of the river. For purposes of the following impact evaluations, it was assumed that temperature decrease within the mixed area (46 m wide x 92 m long) will be proportional to distance from the diffuser pipe. Contact time for organisms drifting through this area will be approximately 1 and 5 minutes at river velocities of 152.5 and 30.5 cm/s, respectively (Section 5.1.2).
Phytoplankton, Periphyton, Macrophytes, Zooplankton, Macroinvertebrates: Drifting phytoplankton, zooplankton, and macroinvertebrates that pass over the discharge structure will be subjected to a temperature change. However an adverse effect is unlikely because of the relatively small temperature change and short contact time. Periphyton, macrophytes, and sedentary benthic macroinvertebrates downriver of the diffuser pipe will be Rev. 2, 12/81 5.1-8
LGS EROL in constant contact with the discharge. With the exception of a small area immediately downriver of the discharge, no measureable change in community structure or productivity is expected because of the small temperature difference.
Fish: Effects of thermal discharge on fish populations are expected to be minor and generally limited to a small area in the vicinity of the diffuser. Under no condition will the discharge pose a block to migrating anadromous fishes. Drifting larvae and downstream moving adults which pass through the discharge area will be subject to temperature change, but because of the rapid transit time and small temperature difference, no mortality is expected. Temperatures near the diffuser will occasionally exceed upper avoidance levels for important species (Tables 5.1-5 and 6). Some displacement of fish from the immediate area may occur. During most of the year temperatures near the diffuser will be attractive to some species (Table 5.1-7). Fish attracted to the discharge will also have increased contact time with other blowdown constituents (Section 5.3). The impact of individual reactions to the altered thermal regime will be minor at the population level because of the small area involved.
In the event of rapid plant shutdown, fish near the diffuser may be subject to a drop in temperature of up to 11.1 0 C (20 0 F) (see Table 5.1-1). The effect of temperature change depends on the rate and magnitude of the temperature decline. The small discharge volume and the small delta T values (Tables 3.3-1 and 5.1-1) outside of the 0.4-ha mixing area indicate the potential for significant impact due to cold shock is small.
5.1.3.2 Perkiomen Creek 5.1.3.2.1 Diversion Low flow in summer and fall may be a problem in Perkiomen Creek, especially in dry years. Low flow stresses biota by reducing wetted area, velocity, depth, and often cover (Johnson Ref 5.1-13). Flow augmentation, especially during the low flow period of dry years, should improve aquatic habitat in Perkiomen Creek between the East Branch confluence and the Graterford intake (3.9 km), and thereby result in a slight increase in productivity of periphyton and benthos if newly wetted areas are submerged long enough for colonization. A reduction in densities of drifting biota may occur initially and throughout diversion if production is not proportional to flow augmentation. Flow augmentation is not expected to cause changes in species composition. Flow augmentation plus natural flow will fall within the natural range of flow variation presently experienced.
The unlikely event of a complete interruption of diversion flow (i.e., accidental pump shutdown) would cause a temporary reduction in abundance of some biotic components in low flow years. Populations will recover following resumption of 5.1-9 Rev. 2, 12/81
LGS EROL augmentation, the rate depending on the population affected, the time of year, and the duration of interruption. The redundancy of the power supply to the pumping station, pumping capacity, and the provision of emergency storage at Bradshaw Reservoir should essentially preclude a complete interruption. The introduction of new species via flow augmentation is possible and is discussed in Section 5.1.3.3.
5.1.3.2.2 Intake A general discussion of intake effects on aquatic biota is given in Section 5.1.3.1.1. Due to constraints placed on the use of water from Perkiomen Creek (Section 2.4.1), operation of the Graterford intake and subsequent impacts to biota will be limited generally to the period April through November. Specific operating times will vary among years, depending on water flow.
At average withdrawal (1.5 m /s) a relatively large portion of water will be withdrawn; 16.0% of average flow (7.9 m /s, April-November) plus diversion, 75.0% of 7-day, 10-year low flow (0.5 m /s) plus diversion, and 93.8% of lowest recorded flow (0.1 m /s) plus diversion. In addition, occasions will arise infrequently when water can be withdrawn from Perkiomen Creek without augmentation; at average withdrawal under these conditions, a maximum of 26% of flow would be withdrawn.
The intake represents latest technology and will consist of a cylindrical wedge-wire screening system (Johnson screen, Section 3.4). The intake screens will be located in the center of the creek parallel with flow and will remain submerged even at extreme low flow. At maximum withdrawal (1.84 m /s) average velocity through the 2-mm screen slots will be 0.13 m/s; the maximum velocity will be 0.14 m/s.
- a. Impingement Few macroinvertebrates and juvenile and adult fishes are expected to be impinged.
Macroinvertebrates: Intake operation is expected to affect only subsurface drift. Chironomidae, Hydropsyche, Cheumatopsyche, Baetis, and Naididae (Oligochaeta) were most abundant in drift (Section 2.2.2.2.6) and therefore are subject to greatest impact.
Losses due to impingement and entrainment are difficult to separate because many aquatic macroinvertebrates exceed 2 mm in length or width. Based on worst case conditions (100% mortality of all entrained and impinged organisms), and using the average predicted withdrawal rate of 1.5 m /s, daily impingement plus entrainment loss was estimated for each of the 24-hour drift studies conducted in the immediate vicinity of the proposed Rev. 2, 12/81 5.1-10
LGS EROL intake. (The impact of Johnson screens on macrobenthos has only begun to be evaluated, but actual losses will probably be considerably less than with conventional screens (Hanson et al, Ref 5.1-14). Estimates for all taxa combined ranged from 4.19 x 104 to 1.52 x 106 (mean 5.44 x 105) organisms, and 5.6 to 82.9 (mean 29.5) g dry weight. The average numerical and biomass losses were equivalent to the standing crop of invertebrates on roughly 41 m2 of stream bottom (or a 1.3-m reach; the channel width near the intake is approximately 64 m) and 7.6 M 2 (0.2-m reach), respectively. These equivalencies were based on estimates of mean benthic standing crop/m 2 (13,283 organisms, 3.9 g dry wt) for the same 13-month period at Rahns (P13600) located 0.8 km downstream of the drift sampling site.
The percentage of bottom fauna drifting at any given time is generally considered to be very low; no more than 0.5%, and usually less than 0.01% (Waters, Ref 5.1-16, based on the formula of Elliott (Ref 5.1-15): P=xD*100 divided by X - xD where x is the number of drifters per m3 , X is the benthic density per m 2 ,
and D is average stream depth in m). Estimates for Perkiomen Creek in 1973 ranged from 0.002 to 0.132% (Rutter and Poe, Ref 5.1-17). In addition the potential for rapid spatial recovery of drift in streams has been demonstrated (McLay, Ref 5.1-18; Townsend and Hildrew, Ref 5.1-19).
For these reasons impingement plus entrainment of drifting macroinvertebrates is expected to have little impact on local macroinvertebrate populations or fish which feed on drift.
Fish: The Graterford intake location is not an area of concentrated abundance for any of the important fishes selected in Section 2.2.2.2.7. Although spawning, localized movement, and feeding occur in the intake vicinity, the area is not of unique importance for these activities. No rare, endangered, or commercially valuable species presently inhabit this reach of the creek. The Perkiomen Creek near Graterford supports an active sport fishery (bass and sunfish), and it is possible that American shad may gain access to the creek if shad restoration efforts on the Schuylkill are successful (see Section 5.1.3.1.1).
Although a large portion of augmented source water will be withdrawn, potential for fish contact with the screen is low because of the screen's orientation parallel to creek flow (Cook, Ref 5.1-20). Fish which contact the screen should easily escape because intake velocity decreases rapidly with distance from the screen. The screen's cylindrical configuration and placement in the water column preclude entrapment. This screen will virtually eliminate impingement as a source of impact on the important species discussed in Section 2.2.2.2.7.
5.1-11
LGS EROL
- b. Entrainment Drifting phytoplankton, zooplankton, benthic macroinvertebrates, and fish eggs and larvae will be entrained by the Graterford intake. Withdrawal projections summarized in Table 5.1-8 were used to estimate entrainment. It is assumed that all drifting biota, except fish eggs and larvae, are uniformly distributed in the water column, and that entrainment loss will be proportional to water withdrawn. Fish eggs and larvae were not uniformly distributed in the creek near the intake site. Therefore losses of these organisms were estimated from densities within the portion of water withdrawn.
Phytoplankton and Zooplankton: Water withdrawal is expected to lower numbers of phytoplankton and zooplankton for a short distance downstream of the intake. Numbers of drifting organisms will be reduced, but the density will not change, assuming uniform distribution. The impact of these reductions is expected to be minor because (1) phytoplankton is known and zooplankton is presumed to be naturally very low in abundance in Perkiomen Creek
. (Sections 2.2.2.2.2 and 2.2.2.2.5), and probably play a minor role in the aquatic community, (2) most phytoplankton in Perkiomen Creek is dislodged periphyton that continually enters the drift, and (3) zooplankton generally reproduces in backwater areas and therefore losses should be compensated a short distance downstream.
Macroinvertebrates: Invertebrate entrainment was discussed previously with impingement.
Fish: Important species (Section 2.2.2.2.7) which reproduce in Perkiomen Creek near Graterford either construct nests or broadcast adhesive eggs. As a result few eggs enter the water column and only a small percentage of the total number spawned are expected to be withdrawn.
The importance of larval drift and the effects of entrainment on fish populations were discussed in Section 5.1.3.1.1. Because water withdrawal will occur during the spawning season (Section 2.4.1), and because a large proportion of the source water body will be removed, the potential impact of entrainment on fish populations in Perkiomen Creek can be regarded as high (based on EPA criteria, USEPA: p. 19, Ref 5.1-8). However the Johnson screen and its midstream location (larvae in Perkiomen Creek generally drift in higher densities along either shore, Section 2.2.2.2.7) should reduce entrainment impact (Heuer and STomljanovich, Ref 5.1-21; Hanson et al, Ref 5.1-14).
5.1-12
LGS EROL Estimates of larval entrainment loss based on 1975 and 1976 data are presented in Table 5.1-9. Percentage of total drift entrained was influenced by horizontal larval drift distribution and proportion of total flow withdrawn. Fish that hypothetically would have suffered the greatest losses drifted in highest density within the influence of the intake (midstream).
Estimates of seasonal loss are not possible based on four sample dates; however, entrainment impact will be mitigated by the design midstream location of the wedge wire screen.
As described in Section 2.4.1, the high flows in 1975 would have allowed consumptive use of the Schuylkill River through June. In more typical flow years withdrawal from Perkiomen Creek will commence in late April or early May. Under these conditions losses of early spawning minnows, white suckers, tessellated darters, and shield darters would occur, as well as additional losses of carp and goldfish (Section 2.2.2.2.7). Also, withdrawal in average years, when creek flow is less than that which occurred in 1975, will probably result in greater loss (both numbers and percent of total drift entrained) of each taxon than estimated because a greater portion of stream flow and larval drift will be removed.
- c. Downstream Water Fluctuations Flows will fluctuate downstream of the intake due to variable water withdrawal. When both LGS units are operating, water will be withdrawn by two pumps.
Variation in withdrawal rates and downstream flow may range up to 0.9 m3 /s. Effects of such variation will be most pronounced during extreme low flows.
Phytoplankton, Periphyton, Macrophytes, Zooplankton, Macroinvertebrates: Flow fluctuations will most affect attached and sedentary organisms (periphyton, macrophytes, benthic macroinvertebrates). Alternate wetting and drying will probably reduce their numbers and production. However, ecosystem impact is expected to be minor because presumably only a small percentage of stream width will be involved. Only minor changes are expected in phytoplankton or zooplankton numbers.
Fish: Fish populations downstream of the intake may be indirectly affected by changes in food production, and directly affected by alteration of near-shore nursery habitat. However since fish populations of Perkiomen Creek have evolved in a fluctuating flow regime, these stresses should not alter fish community structure.
5.1-13
LGS EROL 5.1.3.3 East Branch Perkiomen Creek: Diversion Diversion of Delaware River water through East Branch Perkiomen Creek will markedly alter flow characteristics of the creek, particularly in the headwaters. Augmentation of 1.5 m 3 /s 3
(average, 0.8-1.8 m /s range) is projected to begin in spring or early summer and continue through the low flow season into fall.
Augmentation may be temporarily discontinued during high-flow periods. Flow will be contained within the present channel; the only channel modifications will be at the outside banks of bends to prevent erosion. Delaware River water quality is compatible with that of the East Branch, and no appreciable temperature differences are expected.
Results of augmentation will be most evident in the headwaters, where present flows are frequently <0.03 m3 /s during the year, and current velocities are virtually zero during summer.
Immediately after initiation of diversion, scouring of the streambed, increased siltation, channel modification, and bank flooding will occur. These effects will be temporary and will end when the channel becomes stablized to the new flows. Based on comparison of present low and high flows, stream width will double, depth triple, and velocity will exceed 0.9 m/s in riffle areas of the headwaters. The stabilized channel will contain new run and riffle habitats, pool areas may be eliminated in the headwaters, and substrates could change to coarser materials.
Termination of intermittent summer conditions (see Section 2.2.2.3.1) will occur.
Downstream areas will be less affected by diversion, but changes in stream hydrology can also be expected. The magnitude of change will depend on the configuration of the streambed. The most important result of augmentation downstream will be an improvement in water quality through dilution of the Sellersville Municipal Treatment Plant effluent, the polluted Indian Creek discharge, and farmland runoff (See Section 2.2.2.3.1).
Flow augmentation will introduce biota from the Delaware River and Bradshaw Reservoir. Viability of introduced species will depend in part on survival through the transit system. After passing the intake pumps at Point Pleasant, entrained organisms will pass through 4.3 km of 1.5-m pressure pipe to Bradshaw Reservoir, a 274 x 274 x 4.6 meter deep man made storage impoundment. From Bradshaw, biota will pass through more intake pumps, 9.3 km of 1.1-m pressure pipe, and 1.5 km of 91-cm gravity-flow culvert to an energy dissipator in the East Branch headwaters. Transit time through the pipeline will be approximately three hours, and residence time in Bradshaw is estimated as 17 hours1.967593e-4 days <br />0.00472 hours <br />2.810847e-5 weeks <br />6.4685e-6 months <br />.
5.1-14
LGS EROL Phytoplankton: Phytoplankton is typically low in density and of periphytic origin in shallow, temperate headwater streams.
Augmentation could cause increased periphyton scouring resulting in increased phytoplankton numbers. The density however will remain low due to increased flow. Little impact is expected.
Periphyton: Diversion is expected to affect periphyton through changes in density and biomass. Increased water velocity may cause greater scouring and therefore decreased densities.
However, increased wetted area will provide more substrate for attachment, potentially resulting in an overall increase in biomass. Greatest changes are expected in the upper reaches where intermittent flow presently exists in summer. Effects will be somewhat attenuated in middle and downstream reaches because of naturally higher flows. Diversion could alter community composition. Dilution of point source discharges should not have an affect on periphyton growth because sufficient nutrients would still be present.
Macrophytes: Macrophytes are not common. Scouring may affect existing plants, particularly in the headwaters, but increased wetted area will provide additional macrophyte habitat.
Zooplankton: Zooplankton is typically low in density in small, temperate streams. Diversion will not significantly alter the stream conditions necessary for zooplankton growth. Minimal impact is anticipated.
Macroinvertebrates: Diversion is expected to be generally beneficial to creek macrobenthos. Perturbations which presently operate on the East Branch to reduce invertebrate standing crop (intermittency) and taxonomic richness (degraded water quality) will be ameliorated as a result of flow augmentation.
It is expected that East Branch benthic fauna will show a gradational spatial response to diversion. The proposed maintenance of a 0.8-m3 /s minimum flow until the end of the low flow period (November) would prevent intermittent conditions in the headwaters, thus increasing benthic production. Ward (Ref 5.1-22) in his review of effects of stream flow regulation concluded that extended periods of uniform flow were generally beneficial to benthos. Newly inundated substrate throughout the affected area will eventually become permanently colonized through drift from upstream sections, and from multidirectional movements of benthic organisms over and within the substrate.
Full colonization typically occurs within 30 to 60 days (Mason, Ref 5.1-23, Poole and Stewart, Ref 5.1-24, Sheldon, Ref 5.1-25).
The absence of existing intermittent conditions due to the diversion will also be accompanied by a change in benthic community structure. For example at Elephant Station (E36725) the important (dominant) species Allocapnia vivipara, Perlesta 5.1-15
LGS EROL W placida, and Corixidae (Sigara modesta, Trichocorixa calva) will undoubtedly be reduced in density, whereas other taxa (e.g.,
Hydropsychidae) will increase. In addition, annual creek diversity will probably decrease since there will no longer be a prolonged seasonal habitat change (i.e., riffle to pool, see Section 2.2.2.2.6) in the headwaters.
A benthic response (i.e., change in community structure) to improved water quality is also expected to occur, particularly in the middle reaches, which are presently stressed by stormdrain runoff and the Sellersville Sewage Treatment Plant effluent (Section 2.2.2.3.1). The benthos stations most severely stressed are Sellersville (E26700) and Cathill (E23000) (Section 2.2.2.2.6). Important taxa that will be most affected by a change in water quality are Oligochaeta, Physa acuta,.and Sphaerium at Sellersville, and Oligochaeta and Physa acuta at Cathill. Diversity at Cathill should increase significantly.
Based on flow regime, substrate composition, faunal assemblage, and magnitude of stress, it is expected that changes in benthic community structure associated with elimination of intermittent conditions and improved water quality will result in benthic faunas more like that presently found at Moyer (E12500) station.
. Such a shift would be beneficial, since benthic standing crops (and presumably productivity) here were higher than at any other upstream station, and diversity was relatively high (Section 2.2.2.2.6).
Fluctuations in discharge volume and velocity during augmentation are not expected to influence the changes discussed above.
Spates are a common occurrence on East Branch Perkiomen Creek, and existing communities are adapted to, and recover rapidly (1-3 weeks) from, this stress.
Diversion interruption (an unlikely event, see Section 5.1.3.2.1) for a prolonged period after newly inundated substrate has been colonized would cause differential mortality of stranded benthos (Ward, Ref 5.1-22). When an area is exposed the primary producers are destroyed, and until algae and higher plants are re-established in an area that has been denuded, invertebrates will not return in their former numbers (Waters, Ref 5.1-26).
The effect of flow augmentation on invertebrate drift is difficult to predict or assess. Walton et al (Ref 5.1-27), in their literature review, found that most studies on the effect of current velocity on drift have been descriptive in natural streams, and concluded that the general role of velocity in drift remains obscure. In general, drift rates (number of organisms
. passing a given point per unit time) have been found to increase with increasing velocity, but inverse (Hynes, Ref 5.1-28), direct (Brooker and Hemsworth, Ref 5.1-29), and nondetectable (Elliott, Ref 5.1-15, Anderson and Lehmkuhl, Ref 5.1-30, Ciborowski et al, 5.1-16
LGS EROL Ref 5.1-31) effects on drift density (number per unit volume) have been reported.
On the East Branch, drift rates will undoubtedly increase initially with augmentation due to increased velocity and an anticipated accompanying catastrophic drift response (Waters, Ref 5.1-16), but assuming incoming water is essentially devoid of drifters, the discharge, like a spate, will subsequently dilute existing drift densities throughout the affected area. Unlike a spate however, discharge dilution will continue proportional to the volume pumped. Dilution would be greatest in the headwaters, where incoming water will represent the largest percentage of total water, and least near the confluence. Drift densities will increase somewhat as newly inundated substrate is colonized, but the areal extent of this compensation is unknown.
Qualitative investigations near the proposed Delaware River intake indicated the presence of macroinvertebrates not recorded from East Branch Perkiomen Creek. It is assumed that all entrained aquatic invertebrate species are capable of surviving transport to the East Branch either as egg, immature, or adult.
Newly introduced species may (1) never gain a foothold, (2) compete with other species and eventually displace or replace them, or (3) occupy a previously unexploited niche. For example, Gammarus appeared to be abundant at Point Pleasant. With exception of the isolated occurrence of Hyallela azteca in the headwaters, essentially no other amphipods were found in East Branch Perkiomen Creek. It is possible therefore that once introduced, this omnivore may become established in the East Branch and provide a stable food base readily utilized by fish.
High incidence of the parasitic copepod Argulus sp. was observed during sampling near Gilbert Generating Station, 22.5 km upriver of Point Pleasant. This copepod has not been reported from East Branch Perkiomen Creek. Argulus sp. is commonly found on the body, fins (Hoffman: p. 11, Ref 5.1-32), and gills (Davis:
- p. 197, Ref 5.1-33) of many freshwater fishes.
Fish: Initiation of augmentation will have a temporary adverse affect on the fish community, especially in the headwaters.
Initiation of diversion in April, prior to most spawning, and resultant alteration of substrate, may decrease availability of suitable spawning habitat for some species. If diversion is initiated in May or June there may be destruction of nests, increased egg mortality due to siltation and scouring, increased larval mortalities from physical abrasion, and downstream flushing of larvae, young, and some adults. While the channel is stabilizing to the new flows, a temporary redistribution of adults will occur, and growth of species may be interrupted due to siltation and disturbance of the food supply. Downstream effects of augmentation initiation will be less serious, but some disruption of spawning may occur.
5.1-17
LGS EROL The long term response of the fish community to hydrology changes will be a redistribution of species. Discharge, stream width, depth, and velocity all control fish distribution in streams (Hynes: p. 326-336, Ref 5.1-34; Fraser; Ref 5.1-35). Species adapted to swifter velocities, deeper water, and coarser substrates will find more suitable breeding areas in the headwaters, while those adapted to present low-flow habitat will find less. In downstream reaches augmentation will provide additional spawning and adult habitat which will be beneficial to species already present. Improvement of water quality, particularly below Sellersville, will enable pollution-intolerant species to prosper. Pollution-tolerant species may decrease in abundance because their competitive advantage will be reduced.
Important species in the East Branch (Section 2.2.2.3.7) are distributed according to the range in habitats available. Most species have narrow preferences for current velocity and depth, and have adapted spawning activities to existing breeding habitat. Timing of spawning is often affected by stream flow, particularly in migratory species. Water quality also affects species throughout their life cycle. Therefore each species in the creek will respond differently to the increased flow caused by diversion.
Redfin pickerel, present in the East Branch headwaters and tributaries, will probably be the most affected species because its preferred habitat of sluggish, heavily-vegetated (macrophytes or periphyton) water will be much reduced after augmentation.
This species is apparently dependent upon the pool conditions that occur in summer. Although it may be eliminated from some diversion-affected areas, it will not be eliminated from the creek since suitable habitat is available upstream of the point of discharge and in tributaries. Although redfin pickerel is considered a game species in some drainages, there will be little effect on the recreational fishery here. Angling for redfin pickerel on upper East Branch Perkiomen Creek is virtually nonexistant due to small adult size and scarcity of suitable fishing areas.
Satinfin shiner, common shiner, and spotfin shiner are common in most of the East Branch, but relatively uncommon in the headwaters. Intermittent conditions during the summer may presently limit production of these species. The common shiner requires gravel substrates above riffles for spawning, and this habitat is expected to increase after diversion. Satinfin and spotfin shiners prefer slower-moving water, so success of these species will depend on presence of quiet shallow areas near shore. Eggs of all three species are deposited in crevices or among rocks. During augmentation adults will find headwater habitat more similar to present conditions downstream where they are more abundant. The common shiner will also benefit from improved water quality below Sellersville.
5.1-18
LGS EROL The white sucker, abundant in most areas of the creek, migrates upstream in spring to spawn. Increased discharge at-Elephant Road may affect the location of breeding habitat. Although white suckers may utilize many habitats and substrates for reproduction, gravel and flowing water are usually a necessity.
Both will radically increase in the headwaters during diversion, and because of the sudden flow decrease above the discharge point, a concentration of spawning activity may occur near Elephant Road. More run area will provide more habitat for adults throughout the creek.
The yellow bullhead reproduces under stream banks in relatively deep (0.5-1.2 m) water, a habitat uncommon in the headwaters in June and July. Increases in depth and current velocity will probably cause more undercutting of banks and increase the spawning habitat. Success of young and adults, however, may depend on the development of slow-moving run habitat with aquatic vegetation.
Redbreast sunfish, pumpkinseed, and green sunfish exhibit distributional patterns related to present stream hydrology, morphology, and water quality. Following diversion, changes in distribution are expected. The redbreast sunfish is low in abundance in the headwaters, possibly because of lack of flow, and low in abundance below Sellersville because of poor water quality. Both situations will change, and consequently this species will benefit from diversion. The pumpkinseed requires habitat similar to the redfin pickerel, and increased flow will be detrimental to its success in the headwaters. The green sunfish is most abundant below Sellersville, indicating tolerance to degraded water quality. Elsewhere in the creek this species is relatively common, but it appears to be less successful than redbreast sunfish where they co-exist. Improved water quality therefore may be detrimental to the green sunfish by enabling redbreast sunfish to prosper.
Smallmouth bass may be the species most benefited by diversion.
Presently the species is abundant only in the downstream reach.
Lack of habitat in the headwaters and pollution in midstream areas severely inhibit production elsewhere on the creek.
Diversion will enhance survival of this species throughout the East Branch. Although most collected specimens were young, legal-size bass were collected from three of five sample sites in 1975. Increased food supply will also improve growth, provided turbidity does not increase concurrent with higher discharges.
Termination of intermittent summer conditions and the improvement of smallmouth habitat may provide an improved recreational fishery for this species.
The tessellated darter is abundant in upstream areas, less so below Sellersville. This species appears to adapt to many habitats; adults can be found in quiet water and riffles.
5.1-19
LGS EROL Because spawning occurs in moderate currents, flow augmentation may have little effect on reproduction. Abundance may increase below Sellersville because of improved water quality.
Reduced abundance of hybrid sunfish (Section 2.2.2.3.7) in the headwaters may be caused by increased discharge. Intermittent conditions have been suggested as a major cause of high numbers of hybrids, and diversion will preclude these conditions.
Increased spawning area will cause a reduction in hybridization due to reduced crowding during spawning. The pumpkinseed appears to hybridize more frequently than other species, and its anticipated decrease in abundance may also cause a corresponding decrease in hybrid sunfish.
Eleven fish species not present in the East Branch have been collected from the middle Delaware River. Adults, juveniles, and larvae of sea lamprey, blueback herring, alewife, quillback carpsucker, and walleye; adults of brown trout, channel catfish, white perch, and black crappie; and eggs of American shad were collected in electrofishing, seine, and ichthyoplankton samples near Gilbert Generating Station, approximately 22.5 km upriver of Point Pleasant. Six of these species, and silvery minnow, were captured by seine and trap and fyke nets near the Point Pleasant intake location. Quillback comprised 35% of all larval fish taken, and American shad 28% of all eggs taken at Gilbert. One sea lamprey and nine quillback were collected in entrainment samples.
Blueback herring and white perch eggs and larvae will probably not be entrained at Point Pleasant. Both species spawn nearer the tidal reaches of the Delaware River. Larvae of the remaining nine Delaware River species and eggs of American shad, silvery minnow, and quillback carpsucker may be entrained at Point Pleasant.
Fishes transported from the Delaware River to the East Branch will be exposed to several stresses. Eggs and larvae will experience sudden pressure fluctuations, velocity shear forces, and physical abrasion in the pumps at Point Pleasant and Bradshaw Reservoir and throughout the pipeline. Mortality will vary depending on system design, species, life-history stage, and length (Marcy: pp. 135-138, Ref 5.1-36). It is probable that many entrained organisms will survive transit. Their success in the East Branch will depend on the presence of suitable habitat and the results of interactions with other biota.
Larvae of the anadromous sea lamprey prefer eddies or pools with areas of sandy silt and mud into which they burrow. Although little of this habitat will exist in the headwaters during diversion, suitable areas may exist downstream, particularly in the impoundments. Concentrations of larvae are documented from only two Delaware tributaries (Mihursky, Ref 5.1-37).
5.1-20
LGS EROL Establishment of migratory populations of alewife and American shad is unlikely because of the small size of the East Branch.
While land-locked alewives have been noted, they appear to prefer inland lakes. No land-locked American shad populations have been recorded.
High summer water temperatures will not allow survival of brown trout in the East Branch. The silvery minnow, once found only in the tidal reaches of the Delaware River, now inhabits lower reaches of tributary streams (Mihursky, Ref 5.1-37). This minnow prefers lakes and large wide rivers in this region, and therefore may not be successful in the creek.
Abundance of adult quillback carpsucker is low in the Delaware River, and none have been found in tributary streams. Drifting eggs and larvae are numerous however, and may reach the East Branch. Quillback prefers deep sluggish water in large rivers, and establishment of an adult population in the creek is unlikely. Because of spawning habits and low adult abundance very few if any channel catfish larvae will be entrained at Point Pleasant. Even if introduced, channel catfish would probably not become established in the East Branch because this species prefers moderate to large rivers. Lentic habitat is preferred by black crappie, a rare species in Perkiomen Creek, and absent from the East Branch. Lack of deep water will also preclude successful establishment of walleye.
In the unlikely event of a total pump shutdown, diversion interruption could have an adverse impact on the East Branch fish community, particularly in the headwaters. A sudden decrease in discharge will leave most of the streambed dry, and in summer the creek would revert to a series of pools. Sustained interruption during spawning will expose eggs and larvae and strand individuals in small isolated pools.
5.1.4 EFFECTS OF HEAT DISSIPATION FACILITIES Waste heat from the Limerick Generating Station will be dissipated by two crossflow, natural-draft, cooling towers. Each tower will be 507 feet tall, and located directly north of the turbine-reactor enclosure complex, as shown in Figure 5.1-2. The performance specifications for the cooling towers are given in Section 3.4.
No significant environmental effects on the local agriculture, housing, highways, recreational facilities, or airports are expected from operation of the cooling system.
5.1-21
LGS EROL 5.1.4.1 Predicted Climatology of Visible Plume Geometry Several computer models have been developed to predict the rise and persistence of visible plumes from natural draft cooling towers. Policastro et al (Ref 5.1-38) have recently compared the predictions from all of the available models with plume measurements made in the field. Their results indicate that while some progress is being made toward realistically modeling the plume behavior from a single tower, none of the currently available models are adequate to predict the plume geometry from multiple cooling tower installations such as Limerick. It is expected that to the degree the plumes interact, the plume rise will be increased.
An alternative method for providing climatological estimates of visible plume rise and persistence has been described by Brennan et al (Ref 5.1-39). This method is based upon empirical relationships derived from aircraft measurements of natural draft cooling tower plumes at the John E. Amos plant in West Virginia (Refs 5.1-40 and 41). Amos is a 2900 MW fossil plant with waste heat roughly equivalent to that generated by a 2200 MW nuclear plant such as Limerick. Plume rise and persistence are determined using inversion height and saturation deficit criteria obtained from upper air temperature and humidity soundings. The Amos measurements showed that ground-level meteorology had little influence on the elevated plume behavior.
This latter method has been selected for the Limerick evaluation, using Philadelphia NWS upper air sounding data (Ref 5.1-42) as input.
5.1.4.1.1 Criteria Used in the Plume Analysis The methodology described by Brennan et al (Ref 5.1-39) is based upon the relationship between the final rise of the visible plume and the capping inversion height, and upon saturation deficit as described by Kramer et al (Refs 5.1-41 and -43). The algorithm used to analyze each NWS upper air sounding is described in the following sections.
5.1.4.1.1.1 Plume Rise Criteria Each sounding was first scanned for the presence of an upper-level capping inversion. Inversions below the 950 millibar level (approximately 1800 feet MSL) were discounted, since field observations have indicated that low-level inversions have no appreciable effect on the final plume rise. The base of the upper-level inversion was then designated as the height of the final plume rise. In cases where no inversion was present, the climatological mixing height obtained from Holzworth (Ref 5.1-44) was used as an approximation of the final plume rise.
5.1-22
LGS EROL In order to determine whether the visible plume would reach the inversion base or evaporate while still rising, a mean saturation deficit was computed for the layer of the atmosphere extending from the surface to the inversion base. Kramer et al (Ref 5.1-41) have shown that a mean saturation deficit in this layer greater than 2.5 g/m 3 will cause the plume to evaporate before reaching the inversion.
5.1.4.1.1.2 Visible Plume Length Criteria All soundings which indicated that the visible plume would rise to the inversion base were then examined to determine the predicted plume length. Kramer et al (Ref 5.1-43) found no systematic relationship between the final plume length and the surface saturation deficit. However, they were able to make a distinction between long and short plumes based on the saturation deficit at the plume centerline. Long plumes are defined as those greater than two miles, and short plumes are those less than two miles. The plume centerline saturation deficit was obtained from the first data point below the inversion base on each upper-air sounding. All cases where the centerline saturation deficit was less than or equal to 2.0 g/m 3 were designated as long plumes. All cases with a centerline saturation deficit greater than 2.0 g/m 3 were classified as short plumes.
5.1.4.1.2 Meteorological Input Upper air data obtained by the NWS Environmental Meteorological Support Unit (EMSU) at Philadelphia International Airport were used in the cooling tower plume analysis. Philadelphia is the closest location to the site where upper air measurements are made. EMSU stations operate on a sporadic schedule, but soundings are usually taken at 7:00 a.m. and 12:00 noon on Monday through Friday. A total of 237 soundings were taken in the one-year period from November 1974 through October 1975.
Each sounding was evaluated using the above mentioned criteria, and classified according to plume type. This resulted in 237 predicted plumes upon which the analysis has been based. Each predicted plume should be interpreted as representative only of the exact time at which the sounding was made. This is especially true of the early morning soundings. The Amos tests showed that a typical 7:00 a.m. plume will shorten dramatically during the ensuing hours due to increases in ambient temperature, convective activity, and inversion height.
Any statistics describing the visible plume geometry are also dependent on the season of the year. A data set composed primarily of winter morning soundings will produce a much larger frequency of long plumes than one composed of summer afternoon soundings. This is due to the limited capacity of the atmosphere 5.1-23
LGS EROL to absorb excess moisture during low temperatures. The 237 Philadelphia soundings are broken down by month and time of day in Table 5.1-10. It is obvious from the table that the data are biased toward the winter months, when the majority of the long plumes would occur.
5.1.4.1.3 Predicted Plume Dimensions The Philadelphia data have been analyzed as described in the preceding sections to determine the frequency of long, short, and evaporating plumes. Only six cases met the criteria for a plume which rose to equilibrium, but did not persist beyond two miles.
For convenience in the analysis, these "short" plumes have been included with those which evaporated while rising.
Due to the disproportionately large number of winter soundings, it is inappropriate to make quantitative estimates of the expected annual distribution of plume rise and length.
Statements may be made regarding the predicted plume geometry during the winter months, however, and these estimates are compared with the observations of Kramer et al (Ref 5.1-41) to gain some indication of their accuracy.
5.1.4.1.3.1 Predicted Plume Rise A percent frequency distribution of final plume rise for those plumes predicted to rise to an equilibrium height is shown in Table 5.1-11. The main point to be drawn from this table is that on days when the plume does not evaporate while rising, it will level off at an elevation several hundred meters above ground, and in most cases augment an already existing cloud deck. When the Limerick winter morning plumes are compared with the Amos winter morning plumes documented by Kramer et al (Ref 5.1-41), a slight preference for lower rises is noted at Limerick. This is somewhat contradictory, since Holzworth (Ref 5.1-44) predicts higher winter morning mixing heights at Limerick than at Amos.
5.1.4.1.3.2 Predicted Plume Length The distribution of predicted long and evaporating plumes is shown by directional sector in Table 5.1-12. Note that while the directional distribution of evaporating plumes is somewhat random, the distribution of long plumes follows the same pattern as the wind distribution at the site, which is discussed in Section 2.3. Little can be said quantitatively about the frequency of long plumes based upon the Philadelphia soundings.
However, the preference for long plumes on winter mornings is indicative of the expected trend.
When the Limerick predictions are compared with available observations, it appears the frequency of long plumes is being overestimated. Kramer et al (Ref 5.1-41) found 45% of the plumes 5.1-24
LGS EROL to extend beyond two miles during two winters of early morning observations at the Amos plant. The predicted Limerick distribution shown in Table 5.1-12 indicates that 80% of the winter morning plumes would be long. It must be emphasized that these winter morning observations are the extreme case. During most of the time the plant will be operating, the plumes will be much shorter and will evaporate well within the site boundary.
During a series of 244 observations made between November 1973 and August 1974, Smith (Ref 5.1-45) found the visible plume to evaporate within one-half mile of the plant 67% of the time.
These observations were made at several plants of varying size of the Ohio River valley, during a wide range of conditions.
Similar results were found by Bierman et al (Ref 5.1-46) who conducted six months of early morning observations at the 1800 MW Keystone plant in western Pennsylvania. In the period from February through July 1969, 71% of all early morning plumes were observed to evaporate within 1/4 mile. The Keystone complex is composed of four short towers and is not strictly comparable to Limerick, but the geographical proximity makes the results worth noting.
5.1.4.2 Environmental Effects of Natural-Draft Cooling Towers During the early 1970's, a large number of publications appeared in the literature describing the environmental effects associated with natural-draft cooling tower operation. While in some cases these studies were based on actual observations, the majority were based upon theoretical considerations, and are largely speculation on the potential of natural-draft cooling towers to produce environmental effects. As Carson (Ref 5.1-47) has pointed out, all too often these studies have predicted atmospheric effects that do not in fact occur. Recently, data from several field studies have begun to become available. These studies indicate that the magnitude of the environmental effects resulting from cooling tower operation is much less than predicted by early theoretical evaluations and is of no consequence.
5.1.4.2.1 Visible Plumes By far the most obvious environmental effect attributable to natural-draft cooling towers is the visible plume. The visible plume usually begins within the tower structure, and under the proper meteorological conditions may persist for miles downwind, rising thousands of feet above the tower top. The frequency and geographic distribution of these long plumes has been discussed in more detail in Section 5.1.4.1.
5.1-25
LGS EROL W5.1.4.2.1.1 Ground Shadowing The visible plume will cause a slight reduction in the amount of sunlight received downwind of the plant on days conducive to long plumes. Seeman (Ref 5.1-48) has conducted a study at a 1500 MW fossil fuel plant in Europe, and found that a 35% reduction in total radiation is possible at the point of maximum shadowing by a visible plume on a clear day. (Total radiation = solar radiation + whole sky radiation). On a cloudy day, the maximum shadowing effect is a 20% reduction in total radiation for short periods of time. Due to the variability in wind direction, the plume moves horizontally and does not remain over any one point for long periods of time, giving the same effect as a passing small cumulus cloud. However, Ryznar (Ref 5.1-49) has measured increases in solar radiation due to reflection from the side of the visible plume.
The directional distribution of predicted long plumes at the Limerick site is shown in Table 5.1-12. This distribution indicates that the area immediately southeast of the plant will be most frequently shadowed by the visible plume. Thirty-nine percent of the long plumes in Table 5.1-12 occurred on days when the natural cloud cover was less than 50%, indicating a potential for shadowing. While shadowing does have the potential to affect
- local agriculture to a small degree, it should be emphasized that the majority of the long plume days will occur in the winter, when agriculture considerations are minor. The probability of long persistent plumes on summer days with bright sunshine is negligible.
5.1.4.2.1.2 Effect of the Visible Cooling Tower Plume on Airport Operations The only major airport in the vicinity of the Limerick Generating Station is the Pottstown Municipal Airport. This facility is approximately 5 miles northwest of the plant site. It is expected that the Limerick cooling towers will have little or no impact upon the operation of this airport. The visible plume would extend in the direction of the airport only during southeast winds, which occur infrequently (3..6%) at the site.
Even when winds were from the southeast, it is extremely unlikely that a visible plume would persist for the five mile distance to the airport without rising above 1000 feet, which is the minimum cloud ceiling necessary for an airport to remain open under Visual Flight Rules (VFR).
5.1.4.2.1.3 Synergistic Effects of the Cooling Tower Plume Merging with Air Pollutants The only pollutant source close enough to the site to produce any possible interaction with the cooling tower plume is a plastics manufacturing facility 2000 yards to the WNW. SO2 emissions from 5.1-26
LGS EROL this source, according to the Pennsylvania Department of Environmental Resources (Ref 5.1-50) were at a rate of 33.0 grams per second during 1976. Any diffusion formula (for example Turner, Ref 5.1-51) or comparison with measurements of diffusion (Dittenhoffer and Pena, Ref 5.1-52) leads to the conclusion that SO, concentration levels at the LGS will be on the order of 0.03 parts per million or less. These are negligible and representative of rural air quality. There is no expected effect of this gas on the cooling tower emissions from Limerick, nor would the Limerick cooling towers produce any noticeable effect on the SO2 emissions from the plastic manufacturing facility.
The particulate emissions from this facility were 8.2 grams per second during 1976. The contribution of these particulates at the Limerick facility would be 0.001 g/m 3 .
The merging of these plumes or the entrainment of the industrial plume into the cooling towers will be infrequent in any event, due to the necessity for the wind to be from a restricted direction and for a strong inversion to minimize plume rise and dispersion.
5.1.4.2.2 Fog and Icing The most prevalent environmental effects often raised by the public are ground fogging and icing. For natural draft towers neither of these is a problem. In order for fog to occur, the visible plume must intersect the ground surface. If this occurs during temperatures below freezing, the fog will exist as supercooled water and form rime ice as it contacts exposed surfaces. Observations at operating plants indicate that the visible plume rarely if ever intersects the ground surface.
Spurr (Ref 5.1-53) notes that a complex of eight closely-spaced towers in England, a "few detached fragments" of the plume have been observed to reach the ground surface two to three times per year. Hosler (Ref 5.1-54) also reports one such incident at the Keystone plant. However, the cooling towers at both of these plants are much shorter than those being built at Limerick. The added tower height along with a larger tower exit diameter will assure a sufficient rise to prevent downwashing. Observational studies conducted at large scale cooling tower installations in the United States have documented no occurrences of fog or icing attributable to natural-draft cooling towers (Refs 5.1-40, 41, 55, and 56).
Extremely high winds at the cooling tower base have been observed to cause water to spray outside of the tower basin and form ice on the adjacent structures (Ref 5.1-57). This is a localized problem, however, and does not extend beyond the plant exclusion area.
5.1-27
LGS EROL 5.1.4.2.3 Cloud Modification The updraft of heat and water vapor in a natural-draft cooling tower can, under the proper conditions, produce cumulus clouds or augment already existing cloud decks. This phenomenon has been documented by both Smith (Ref 5.1-45) and Spurr (Ref 5.1-53), but it can be expected to occur only when conditions favor natural cloud formation.
5.1.4.2.4 Precipitation Modification Observations of precipitation falling from natural-draft plumes are very limited. Kramer et al (Ref 5.1-58) have documented one observation of light rain falling from a natural-draft plume, and several observations of light snowfall. Though it may be possible for a cooling tower to modify the precipitation pattern immediately downwind of the tower, it will not alter the total precipitation in the region, as the water vapor emissions from the towers are small compared to natural fluxes (Ref 5.1-47).
During the winter of 1975-1976, Kramer et al (Ref 5.1-58) observed light snow from several different cooling towers on ten separate days. Though little is known about the actual precipitation mechanisms causing the snowfall, it was found only during stable atmospheric conditions with temperatures below 10OF at the height of the plume centerline. In the one year of Philadelphia upper air soundings summarized in Section 5.1.4.1, on 22 days, for short periods, the temperature criteria necessary for snowfall were met. This should not be interpreted as a prediction of snowfall frequency. There are several other variables such as atmospheric stability, circulating water chemistry, drift eliminator condition, and condensation nuclei availability which play a role in snowfall formation. The height to which the plume rises is such that in most cases the snow crystals would sublimate before reaching the ground. There is also a strong likelihood that downslope motion to the east would tend to oppose any depth of cloud development with westerly flow.
5.1.4.2.5 Humidity Changes Observational studies have shown that no changes in the ground-level relative humidity should be expected as a result of natural-draft cooling tower operation. In a study of a 2000 MW, eight-tower complex in England, Spurr (Ref 5.1-53) found no differences in the ground-level relative humidity upwind and downwind of the plant.
5.1-28
LGS EROL 5.1.4.2.6 Cooling Tower Drift 5.1.4.2.6.1 Cooling Tower Drift Deposition Calculations Calculations have been made to determine the salt and water deposition rate from the drift originating in the two natural draft cooling towers. The calculations were made following the method of C.L. Hosler, J. Pena and R. Pena (Ref 5.1-59). In this method, the influence of the evaporation of the drift drop is considered and the trajectory of the drift particles is assumed to be determined by their fall velocities and the wind speed.
The effect of turbulent diffusion has not been included in the calculations. A paper by Pena and Hosler (Ref 5.1-60) has shown by comparative calculations that the inclusion of turbulent diffusion does not significantly affect the result.
5.1.4.2.6.1.1 Tower and Operational Characteristics For these calculations the following information is required:
- a. Tower height
- b. Updraft velocity at tower exit
- c. Drift mass fraction
- d. Flow of cooling water
- e. Drift drop size distribution
- f. Plume mean height
- g. Salt concentration in the cooling tower circulating water.
All these data are related to the type of cooling tower and how it is operated, except for the plume height, which also depends upon the meteorological conditions. The input values used for items a, b, c, and d are as follows:
- a. Tower height 507.5 ft
- b. Updraft velocity 23.1 ft/sec tower exit
- c. Drift mass fraction 1.7 x 10-4
- d. Flow of cooling water 476,600 gpm The drift droplet size distribution used is a composite based upon measured size distributions at the Chalk Point cooling tower. The composite distribution is shown below.
5.1-29
LGS EROL Drop size diameter Mass fraction (0m) 50-100 0.401 101-200 0.347 201-300 0.101 301-400 0.068 401-500 0.053 501-600 0.030 Mean plume heights have been determined in Section 5.1.4.1.
Using local soundings obtained during the winter months, the average plume height for that season is expected to average 3280 feet above grade. Because of the seasonal variation of mixing heights, the mean plume height has been adjusted by month according to the monthly values of mixing height given by Holzworth (Ref 5.1-44). These adjusted heights are shown in Table 5.1-13.
The concentration of NaCl in the cooling tower circulating water is also given by month in Table 5.1-13. These values are the result of a field sampling program in the Schuylkill River with the appropriate concentration factors accounted for.
5.1.4.2.6.1.2 Meteorological Input The meteorological parameters required as input for the drift deposition model are as follows:
- a. Relative humidity ranges and frequency,
- b. Wind direction and speed distributions, and
- c. Monthly and annual mean temperatures.
These parameters were obtained onsite using five years of data from Weather Station No. 1. They are summarized in a detailed manner in Section 2.3. However, the actual summaries used in the drift calculations are shown in Tables 5.1-14 through 5.1-17.
The wind data are related to the directional dispersion of the drift. Temperature and humidity are the major influences on the rate of evaporation of the drift drops and therefore on the residence time of the drift particle in the air.
5.1.4.2.6.1.3 Deposition Rate Calculation The first step in the calculation is to determine the mass fraction of the drift drops that do not evaporate or evaporate totally or partially. The concentration of total dissolved solids in the tower basin at Limerick is on the average 700 ppm.
5.1-30
LGS EROL Because of this low concentration it can be expected that the evaporated drift drops will be small and therefore their fall velocities will also be small. It is also expected that they will be deposited at great distances from the tower.
The size of the evaporated drift drops can be estimated if we assume that the salt is sodium chloride (other substances will give different results, but the difference in the final sizes will not exceed 30%). For a sodium chloride solution drop of initial concentration Co, density po, and diameter do, the diameter of the saturated solution drop, d 7 6 , (at 76% relative humidity) and the diameter of a dry particle, d 6 5 , (below 65%
relative humidity), are given by the following formulae:
d76 = 1.48 do (copo) 1/3 d 6 5 = 0.78 do (copo) 1/3 For the Limerick plant:
po = 1, co = 7 x 10-4 The final diameters of the drift particles and their fall velocities are as follows:
Initial Diameter Fall Diameter Fall Diameter at 76% RH Velocity at<65% RH Velocity
(,m) (Mm) (ft/sec) (mm) (ft/sec) dn d 7 .K d vAS 100 13 0.0163 5.7 0.0033 200 26 0.0693 11.4 0.0132 300 39 0.1584 17.1 0.0297 From these results, it can be expected that the residue from the evaporated drift drops will be deposited very far from the tower because of their small fall velocity, resulting in a very small contribution to the desposition rate.
To show the magnitude of the deposition rate for these drops, the following assumptions were made.
- a. All the evaporated drops have an initial diameter of 300 mm,
- b. Their fall velocity is 0.16 ft/sec,
- c. The annual mean wind speed is 13.1 mi/hr, and
- d. The evaporated drops constitute 60% of the drift.
5.1-31
LGS EROL W Using the formula of Sutton, as modified b Holland (Ref 5.1-61),
it isy estimated that the deposition will take place in the range 5 to 10 miles from the tower.
From Table 5.1-18, the deposition rate of NaCl between 1 and 2 miles is on the average 3 lb/acre/yr for the ESE (112.50) sector.
The surface area of this sector between 1 and 2 miles is 1.85 x 106 square yards. If Q is the drift emission rate the deposition rate, w, may be expressed as:
w = 0.4 Q = 3 lb/acre/yr 1.85x106 (5.1-1)
In the range 5-10 miles, the surface area for the same sector is 45.6 x 106 square yards, and the deposition rate, w, will be:
w 0.6 Q 46.5 x 106 (5. 1-2)
By substituting the value of Q from equation (1),
w = 0.6 x 1.85 x 3 = 0.18 lb/acre/yr 0.4 46.5
. This value is in itself very low as a deposition rate, but it is a maximum value because the ESE is the highest deposition sector and because most of the evaporated drift is in the form of smaller particles which will be deposited further away than the assumed 10 miles. The only contributors to deposition at shorter distances from the power plant are the drift drops that reach the ground without achieving evaporation.
The factors determining the deposition of nonevaporated drops are as follows:
- a. Relative humidity in the range 90-100%; this applies to drift drops of all sizes,
- b. Drift drops with a low rate of evaporation as a result of low temperature and relative humidity values less than 90%,
- c. Lower plume height, and
- d. High drift drop fall velocity.
As a result of superposition of conditions b, c, and d, very often the larger sizes in the drift drop distribution do not evaporate.
5.1-32
LGS EROL 5.1.4.2.6.1.4 NaCI Deposition Rate Calculations have been made of the deposition rate of NaCl over the sixteen, 22.50 compass sectors. These deposition rates (monthly and annual) have been calculated on the basis of the mean wind speeds given in Table 5.1-16. The closest distance to the towers for which these calculations were made is the site boundary or 1/2 mile, depending upon the sector.
The annual deposition rate of NaCI is given for each sector at distances of 1/2, 1, and 2 miles in Table 5.1-18. The maximum deposition rate is 6.8 lb/acre/yr at a distance of 1/2 mile in the ESE (112.50) sector. Natural NaCl deposition in the Limerick region is 10 to 15 lb/acre/yr (Ref 5.1-62) which is well above the maximum cooling tower salt deposition rate in Table 5.1-18.
The annual NaCl deposition rate for the site boundary distance in each sector is shown in Table 5.1-19. These values are also well below background levels, with a maximum of 6.7 lb/acre/yr in the ESE sector.
The monthly NaCl deposition rates are given for each sector at a distance of 1/2 mile in Table 5.1-20, and 1 mile in Table 5.1-21.
The maximum monthly deposition rate was 1.06 lbs/acre/month at 1/2 mile in the ESE sector during August.
5.1.4.2.6.1.5 Liquid Water Deposition Most of the drift deposited near the Limerick Generating Station will be as liquid drops. Calculations of the excess deposition of water at the site boundary were made in each sector and then converted to inches of precipitation. The monthly and annual increases in precipitation at the site boundary in each sector are given in Table 5.1-22. The maximum annual increase was .253 inches in the ESE sector. This is an increase of less than 1%
over the annual precipitation total as reported in Section 2.3.
During the months of December, January, and February, a total of 0.055 inches of additional precipitation would be expected at the ESE site boundary. This is insignificant in regard to icing problems.
5.1.4.2.6.2 Drift Effects on Agriculture The impact of NaCl deposition upon local agriculture is discussed in Section 5.3.1.
5.1.4.2.6.3 Drift Effects on Highways The Limerick cooling towers should have no adverse impact upon the local highways. The effect of liquid drift deposition has been previously discussed in Section 5.1.4.2.6.1.5, and shown to be inconsequential at the site boundary. The liquid water deposition will be even less at offsite locations.
5.1-33
LGS EROL 5.1.4.2.7 Environmental Effects of Cooling Tower Blowdown Water The thermal effects of the cooling tower blowdown water are discussed in Section 5.1.3, and the chemical effects are discussed in Section 5.3.1.
5.1.4.2.8 Cooling Tower Noise The noise level resulting from cooling tower operation at the LGS has been predicted using the technique of Capano and Bradley (Ref 5.1-63). This technique is based upon the results of a series of field measurements at large natural draft cooling tower installations. The predicted noise level versus distance from the towers for two cooling towers operating simultaneously is shown in Figure 5.1-3. The USEPA Guideline (Ref 5.1-64) for outdoor noise levels is 55 dB, Ldn, which is equivalent to a constant sound level of 49 dBA. As Figure 5.1-3 shows, the 49 dBA criteria will be met at the exclusion area boundary, and the noise level will be well below standards at the LPZ.
5.1.4.3 Environmental Effects of the Ultimate Heat Sink The ultimate heat sink at the LGS is a spray pond. During routine operations this pond will not be heated, and water temperatures will fluctuate in response to ambient meteorological conditions in the same manner as any natural pond of the same size. This should produce no adverse impact on the environment.
There will be some blowdown of the spray pond for water quality control. The effects of chemicals discharged from the spray pond blowdown are discussed in Section 5.3.
5.1-34
LGS EROL 5.
1.5 REFERENCES
5.1-1 Chapter 93 Water Quality Criteria, Title 25 Pennsylvania Rules and Regulations, Department of Environmental Resources.
5.1-2 G.H. Jirka and D.R.F. Harleman, The Mechanics of Submerged Multiport Diffusers for Buoyant Discharges in Shallow Water, Ralph M. Parsons Laboratory for Water Resources and Hydrodynamics, Massachusetts Institute of Technology, Report No. 169 (March 1973).
5.1-3 Philadelphia Electric Company, Environmental Report Construction Permit Stage (Revised) Limerick Generating Station, Units 1 and 2 (1972).
5.1-4 United States Atomic Energy Commission, Final Environmental Statement Related to the Proposed Limerick Generating Station Units 1 and 2, Docket Nos. 50-352 and 50-353. Philadelphia Electric Company (1973).
5.1-5 Philadelphia Electric Company, Cromby Generating Station: Materials Prepared for the Environmental Protection Agency: 316(b) report (1977a).
5.1-6 Philadelphia Electric Company, Barbadoes Generating Station; Materials Prepared for the Environmental Protection Agency: 316(b) report (1977b).
5.1-7 Philadephia Electric Company, Schuylkill Generating Station: Materials Prepared for the Environmental Protection Agency: 316(b) report (1977c).
5.1-8 United States Environmental Protection Agency, Guidance for Evaluating the Adverse Impact of Cooling Water Intake Structures on the Aquatic Environment, Section 316(b) P.L.92-500, USEPA Industrial Permits Branch, Washington, DC (1977) p. 19.
5.1-9 Harmon, P. L., Survey of Anglers on the Schuylkill River near Pottstown, Pennsylvania in 1976, Pennsylvania Academy of Science, 52: 153-156 (19-78).
5.1-10 Lofton, L., Impingement of Fishes on Water Intake Screens of Maior Industrial Water Users on the Delaware River with Particular Reference to Anadromous Fish, U.S.
Fish and Wildlife Service, Delaware River Basin Anadromous Fishery Project, Special Rep. No. 3 (1976).
5.1-11 Nikolsky, G. V., The Ecology of Fishes, Academic Press, London (1963).
5.1-35
LGS EROL
@ 5.1-12 Dovel, W. L., "Fish Eggs and Larvae of the Upper Chesapeake Bay", Contribution No. 460, Natural Resource Institute Special Report No. 4, University of Maryland (1971).
5.1-13 Johnson, F. W., Minimum Instream Flow Needs for Salmonids and for Other Recreational and Environmental Purposes, Available from Pennsylvania Fish Commission, Harrisburg, Pennsylvania (1977).
5.1-14 Hanson, B. N., W. H. Bason, B. E. Beitz, and K. E.
Charles, "Practicality of Profile-Wire Screen in Reducing Entrainment and Impingement" in Sharma, R. K.,
and J. B. Palmer, eds. Larval Exclusion Systems for Power Plant Cooling Water Intakes, Argonne National Laboratory, Argonne, Illinois (1978) pp. 195-233.
5.1-15 Elliott, J. M., "Invertebrate Drift in a Dartmoor Stream", Archive fur Hydrobiologie 63 (1967) pp. 202-237.
5.1-16 Waters, T. F., "The Drift of Stream Insects", Annual Review of Entemology 17 (1970) pp. 253-272.
5.1-17 Rutter, R. P., and T. P. Poe, "Macroinvertebrate Drift in Two Adjoining Southeastern Pennsylvania Streams",
Pennsylvania Academy Science Vol. 52 (1978) pp. 24-30.
5.1-18 McLay, C., "A Theory Concerning the Distance Travelled by Animals Entering the Drift of a Stream", Journal of Fishery Resources Bulletin of Canada 27 (1970) pp. 359-370.
5.1-19 Townsend, C. R., and A. G. Hildrew, "Field Experiments on the Drifting, Colonization and Continuous Redistribution of Stream Benthos", Journal of Animal Ecology 45 (1976) pp. 759-772.
5.1-20 Cook, L. E., "The Johnson Screen for Cooling Water Intakes" in Sharma, R. K., and J. B. Palmer, eds.
Larval Exclusion Systems for Power Plant Cooling Water Intakes, Argonne National Laboratory, Argonne, Illinois, (1978) pp. 149-157.
5.1-21 Heuer, J. H., and D. A. Tomljanovich, "A Study on the Protection of Fish Larvae at Water Intakes Using Wedgewire Screening", in Sharma, R. K., and J. B.
Palmer, eds. Larval Exclusion Systems for Power Plant Cooling Water Intakes, Argonne National Laboratory,
__ Argonne, Illinois, (1978) pp. 169-194.
5.1-36
LGS EROL 5.1-22 Ward, J. V., "Effects of Flow Patterns Below Large Dams on Stream Benthos", a review in Orsbon, J. F. and C. H.
Allman, eds. "Instream Flow Needs Symposium", Vol II.
American Fishery Society, (1976) pp. 235-253.
5.1-23 Mason, J. C., "Evaluating a Substrate Tray for Sampling the Invertebrate Fauna of Small Streams, with Comment on General Sampling Problems", Archive fur Hydrobiologie 78 (1976) pp. 51-70.
5.1-24 Poole, W. C., and K. W. Stewart, "The Vertical Distribution of Macrobenthos within the Substratum of the Brazos River, Texas", Hydrobiologia 50 (1976) 4pp. 151-160.
5.1-25 Sheldon, A. L., "Colonization Curves: Application to Stream Insects on Semi-natural Substrates." Oikos 28 (1977) pp. 256-261.
5.1-26 Waters, T. F., "Recolonization of Denuded Stream Bottom Areas by Drift", Trans. Am. Fish. Soc. 93 (1964) pp. 311-315.
5.1-27 Walton, 0. E., Jr., S. R. Reice, and R. W. Andrews, "The Effects of Density, Sediment Particle Size and Velocity on Drift of Acroneuria abonormis (Plecoptera)", Oikos 28 (1977) pp. 291-298.
5.1-28 Hynes, J. D., "Downstream Drift of Invertebrates in a River in Southern Ghana", Freshwater Biology 5, (1975) pp. 515-532.
5.1-29 Brooker, M. P., and R. J. Hemsworth, "The Effect of the Release of an Artificial Discharge of Water on Invertebrate Drift in the River Wye, Wales",
Hydrobiologia 59, (1978) pp. 155-163.
5.1-30 Anderson, N. H., and D. M. Lehmkul, "Catastrophic Drift of Insects in a Woodland Stream", Ecology 49, (1968) pp. 198-206.
5.1-31 Ciborowski, J. J. H., P. J. Pointing, and L. D. Corkum, "The Effect of Current Velocity and Sediment on the Drift of the Mayfly Ephemerella subvaria McDunnough",
Freshwater Biology 7, (1977) pp. 567-572.
5.1-32 Hoffman, G. L., Parasites of North American Freshwater Fishes, University of California Press, Berkeley, California, (1967).
5.1-37
LGS EROL 5.1-33 Davis, H. S., Culture and Diseases of Game Fishes, Univeristy of California Press, Berkeley, California (1967).
5.1-34 Hynes, H. B. N., The Ecology of Running Waters, University of Toronto Press (1970).
5.1-35 Fraser, J. C., "Regulated Discharge and the Stream Environment" in Oglesby, R. T., C. A. Carlson, and J. A.
McCann, eds., River Ecology and Man, Academic Press Inc., New York (1972) pp. 263-285.
5.1-36 Marcy, B. C., Jr., "Planktonic Fish Eggs and Larvae of the Lower Connecticut River and the Effects of the Connecticut Yankee Plant including Entrainment", in Merriman, D., and L. Thorpe, eds., "The Connecticut River Ecological Study: The Impact of a Nuclear Power Plant", American Fishery Society Monogram No 1 (1976).
5.1-37 Mihursky, J. A., Fishes of the Middle Lenopewihittuck (Delaware River) Basin, Ph. D. dissertation, Lehign University, Bethlehem, Pennsylvania (1962).
4.1-38 Policastro, A. J., Carhart, R. A. and DeVantier, B.,
Validation of Selected Mathematical Models for Plume Dispersion from Natural Draft Cooling Towers, presented at the Water Heat Management and Utilization Conference, Miami Beach (May 1977).
5.1-39 Brennan, P. T., Seymour, D. E., Butler, M. J., Kramer, M. L., Smith, M. E. and Frankenberg, T. T. "The Observed Rise of Visible Plumes from Hyperbolic Natural Draft Cooling Towers", Atmospheric Environment, Vol 10 (1976) pp. 425-431.
5.1-40 Kramer, M. L. and Seymour, D. E., et al, John E. Amos Cooling Tower Flight Program Data, December 1974 - March 1975, available A.E.P. Service Corporation, Environmental Engineering Division, Canton, Ohio (1975).
5.1-41 Kramer, M. L. and Seymour, D. E., John E. Amos Cooling Tower Flight Program Data, December 1975 - March 1976, available A.E.P. Service Corporation, Environmental Engineering Division, Canton, Ohio (1976).
5.1-42 U. S. Department of Commerce, Environmental Data Service, WBAN 33, Summary of Constant Pressure Data, Philadelphia, Pennsylvania, November 1974 - October 1975, available from National Climatic Center, Ashville, N. C.
5.1-38
LGS EROL 5.1-43 Kramer, M. L., Smith, M. E., Butler, M. J., Seymour, D.
E. and Frankenberg, T. T., "Cooling Towers and the Environment", Journal APCA, Vol. 26, No 8 (1976) pp.
582-584.
5.1-44 Holzworth, G. C., Mixing Heights, Wind Speeds, and Potential for Urban Air Pollution Throughout the Contiguous United States, USEPA, Office of Air Programs (1972).
5.1-45 Smith, M. E., Cooling Towers and the Environment, brochure available from A.E.P. Service Corporation, Environmental Engineering Division, Canton, Ohio (1974).
5.1-46 Bierman, G. F., Kunden, G. A., Sebald, J. F., and Visbisky, R. F., Characteristics, Classification and Incidence of Plumes from Large Natural Draft Cooling Towers, presented at the 33rd Annual Meeting of the American Power Conference, Chicago, Illinois (April 1971).
5.1-47 Carson, J. E., Atmospheric Impacts of Evaporative Cooling Systems, Argonne National Laboratory Report ANL/ES-53 (October 1976).
5..1-48 Seeman, J. et al, Effets Produits sur L'Agriculture par les Ranaches Rejetes par less Tours de Refroidissement dans L'Environment des Centrales Nucleaires Department Etudes Generales-Programmes, Sites-Environment, Paris, France (October 20, 1976).
5.1-49 Ryznar, E., "An Observation of Cooling Tower Plume Effects on Total Solar Radiation", Atmospheric Environment, Vol. 12 (1978) pp. 1223-1224.
5.1-50 S. R. Patel, Personal Communication, Pennsylvania Department of Environmental Resources, (July 18, 1978).
5.1-51 Turner, D. B., Workbook of Atmospheric Dispersion Estimates, USHEW (1969) p. 5.
5.1-52 Dittenhoffer, A. C., and Pena, R. G., "A Study of Production and Growth of Sulfate Particles in Plumes From a Coal-Fired Power Plant," Atmospheric Environment Vol. 12 (1978) pp. 297-306.
5.1-53 Spurr, G., "Meteorology and Cooling Tower Operation",
Atmospheric Environment, Vol. 8 (1974) pp. 321-324.
5.1-54 Hosler, C. L., "Wet Cooling Tower Behavior", in Cooling Towers by the American Institute of Chemical Engineering (1972) pp. 27-32.
- 5. 1-39
LGS EROL 5.1-55 Woffinden, G. J., Harrison, P. R. and Anderson, J. A.,
"Airborne Monitoring of Cooling Tower Effluents," EPRI Report EA-420 (1977).
5.1-56 Slawson, P. R., Coleman, J. H., and Blackwell, P. J.,
"Natural Draft Cooling Water Tower Plume Behavior at Paradise Steam Plant," Tennessee Valley Authority, Division of Environmental Planning, Report No, E-AQ-76-1 (1975) 5.1-57 Brennan, P. T. et al, "Behavior of Visible Plumes from Hyperbolic Cooling Towers", Proceedinos of the American Power Conference, Vol. 38 (1976) pp. 732-739.
5.1-58 Kramer, M. L., et al, "Snowfall Observations. From Natural Draft Cooling Tower Plumes", Science, Vol. 193, (1976) pp. 1239-1241.
5.1-59 Hosler, C. L., Pena, J., and Pena, R., "Determination of Salt Deposition Rates From Drift From Evaporating Cooling Towers", Journal of Engineering for Power, Vol.
96 (1974) pp. 283-291.
5.1-60 Pena, J. A., and Hosler, C. L., "The Influence of the Choice of Plume Diffusion Formula on the Salt Deposition Rate Calculation, Cooling Tower Environment - 1974" ERDA Symposium Series, Conference 740302 (1974) pp. 573-584.
5.1-61 Holland, J. Z., A Meteorological Survey of the Oak Ridge Area, USAEC Reb ORO 99 (1953) p. 540.
5.1-62 Brierly, W. B., "Atmospheric Sea-Salts Design Criteria Areas, Journal of Environmental Science, Vol. (8) 5, (1965) pp. 15-23.
5.1-63 Capano, G. A., and Bradley, W. E., "Noise Prediction Techniques for Siting Large Natural Draft and Mechanical Draft Cooling Towers", Proceedings of the American Power Conference, Vol. 38 (1976) pp. 756-763.
5.1-64 USEPA, Information on Levels of Environmental Noise Requisite to Protect Public Health and Welfare With an Adequate Margin of Safety, PB 239, 429, (EPA-550/9-74-004). Available NTIS.
5.1-65 Cooper, G. P., and J. L. Fuller, "A Biological Survey of Moosehead Lake and Haymock Lake, Maine." Maine Dept.
Inland Fish. Game, Fish Survey Report 6 (Original not seen) (1945) pp. 160.
5.1-40
LGS EROL 5.1-66 Coutant, C. C., "Compilation of Temperature Preference Data", Journal Fishery Resources Bulletin of Canada 34 (1977) pp. 739-745.
5.1-67 Ferguson, R. G., "The Preferred Temperature of Fish and Their Midsummer Distribution in Temperate Lakes and Streams", Journal Fishery Resource Bulletin of Canada, 15 (1958) (Original not seen) pp. 607-624.
5.1-68 Fry, F. E. J., "Effects of the Environment on Animal Activity", University of Toronto Study Biology Ser. 55, Publ. Ont. Fish. Res. Lab. 68, (1947) (Original not seen) pp. 1-62.
5.1-69 Hile, R., and C. Juday, "Bathymetric Distributions of Fish in Lakes of the Northeastern Highlands, Wisconsin,"
Trans. Wis. Acad. Sci. Arts Lett. 33 (1941), (Original not seen) pp. 147-187.
5.1-70 Horak, 0. L., and H. A. Tanner, "The Use of Vertical Gill Nets in Studying Fish Depth Distribution, Horsetooth Reservoir, Colorado," Trans. Am. Fish. Soc.
93, (1964) pp. 137-145.
5.1-71 Reutter, J. M., and C. E. Herdendrof, "Laboratory Estimates of the Seasonal Final Temperature Preferenda of Some Lake Erie Fish," Proc. 17th Conf. Great Lakes Res. 1974 (1975), (Original not seeny pp. 59-67.
5.1-72 Reynolds, W. W., and J. B. Covert, "Behavioral Fever in Aquatic Extothermic Vertebrates" in Karger and Basel, eds. Drugs, Biogenic Amines, and Body Temperature, Proc. 3rd Int. Symp. Pharmacol. Thermoreg., Banff Alberta, 14-17 Sept. 1976, (1977) (Original not seen).
5.1-73 Roy, A. W., and P. H. Johansen, "The Temperature Selection of Small Hypophysectomized Goldfish Carassius auratus L.1)", Canadian Journal of Zoology 48 (1970) pp. 323-326 (Original not seen).
5.1-74 Scott, W. B. and E. J. Crossman, "Freshwater Fishes of Canada", Bulletin 184, Fishery Resource Bulletin of Canada.
5.1-75 Parr, A. D., and Sayre, W. W., "Prototype and Model Studies of the Diffuser Pipe System for Discharging Condenser Cooling Water at the Quad Cities Nuclear Station", IIHR Report No. 204, Iowa Institute of Hydraulic Research, Iowa "Clty, Iowa, June 1977.
5.1-41 Rev. 2, 12/81
LGS EROL TABLE 5.1-1 (Page 1 of 3)
AVERAGE THERMAL DISCHARGE CHARACTERISTICS DURING FULL-POWER OPERATION Cooling Tower Blowdown Temperature 50% Exceedance Schuylkill Temperature Temperature River Diffuser Difference Rise 50 ft Heat 1Aoad Flowrate Flow Dilution Blowdown- Downstreamn Dischalrged Month JMjGD=CFS) Factor RiverF in RiverqOF_ IBTU/h our.L Jan 2244 20.3 = 31.4 0. 042 61-42 = 19 0.8 134 x 106 Feb 2457 20.3 = 31.4 0.038 61-41 = 20 0.8 141 x 106 Mar 3217 18.3 = 28.3 0.026 65-48 = 17 0.4 108 x 106 Apr 2900 16.1 = 24.9 0.026 70-53 = 17 0.4 95 x 106 May 2218 14.1 = 21.8 0.029 76-63 = 13 0.4 64 x 106 Jun 1513 16.3 = 25.2 0.050 82-72 = 10 0.5 57 x 106 Jul 1248 16.3 = 25.2 0.061 84-76 = 8 0.5 45 x 106 Aug 1090 16.3 = 25.2 0.069 84-78 = 6 0.4 34 x 106 Sep 1080 16.3 = 25.2 0.070 79-72 = 7 0.5 40 x 1 06 Oct 1154 16.3 = 25.2 0.066 73-61 = 12 0.8 68 x 106 Nov 1701 17.7 = 27.4 0.048 66-53 = 13 0.6 80 x 106 Dec 2093 19.7 = 31.5 0.044 62-45 = 17 0.7 116 x 106 Annual 1910 17.3 = 26.8 0. 042 72-59 = 13 0.5 78 x 106 (l) 260 12.4 = 19.2 0.222 73-61 = 12 2.7 52 x 106 Cl) Extreme condition with 7-day, 10-year low river flow of 260 cfs and limited diffuser flow occurring with October river temperatures and October cooling tower blowdown temperatures that are exceeded only 50, 5, 1% of time respectively. October temperature differences were selected because this month would be most likely to contain the combination of low flow and high temperature difference.
Rev. 2, 12/81
0 LGS EROL TABLE 5.1-1 (CONTID) (Page 2 of 3) mmm Cooling Tower-Blowdown Temperature X Eceedance Schuylkill Temperature Temperature River Diffuser Difference Rise 50 ft Heat L :ead Flowrate Flow Di lution Blowd own- Downstream Dischaj rged Month _.L*GD=CFSj__ Factor River (OF)_ inRiver -(O) QT U/h_o)urj Jan 2244 20.3 31.4 0.042 72-42 = 30 1.3 212 x 106 Feb 2457 20.3 31.4 0.038 72-41 = 31 1.2 219 'C 106 Mar 3217 18.3 28.3 0.026 76-48 = 28 0.7 178 x 106 Apr 2900 16.1 24.9 0.026 82-53 = 29 0.7 162 x 106 May 2218 14.1 21.8 0. 029 86-63 = 23 0.7 113 x 106 Jun 1513 16.3 25.2 0.050 89-72 = 17 0.8 96 'C 106 Jul 1248 16.3 25.2 0.061 91-76 = 15 0.9 85 x 106 Aug 1090 16.3 25.2 0.069 91-78 = 13 0.9 74 x 106 Sep 1080 16.3 25.2 0.070 87-72 = 15 1.1 85 x 106 Oct 1154 16.3 25.2 0.066 83-61 = 22 1.4 125 x 106 Nov. 1701 17.7 27.4 0.048 80-53 = 27 1.3 166 x 106 Dec 2093 19.7 31.5 0.044 72-45 = 27 1.2 185 x 106 Annual 1910 17.3 = 26.8 0.042 88-59 = 29 1.2 175 x 106 (1) 260 12.4 = 19.2 0.222 83-61 = 22 4.9 95 x .106 (1) Extreme condition with 7-day, 10-year low river flow of 260 cfs and limited diffuser flow occurring with October river temperatures and October cooling tower blowdown temperatures that are exceeded only 50, 5, 1% of time respectively. October temperature differences were selected because this month would be most likely to contain the combination of low flow and high temperature difference.
Rev. 2, 12/81
0 LGS EROL TABLE 5.1-1 (CONT'D) (Page 3 of 3)
Coolina Tower Blowdown Temperature 1% Exceedance Schuylkill Temperature Temperature River Diffuser Difference Rise 50 ft Heat Load Flowrate Flow Dilution Blowdown- Downstream Discharged Month _(Lcfs§I-_ _LMGD=CFS) Factor River (OFL in River_?Fl _(BTU/hour)
Jan 2244 20.3 = 31.4 0.042 77-42 = 35 1.5 247 x 106 Feb 2457 20.3 = 31.4 0. 038 77-41 = 36 1.4 254 x 106 Mar 3217 18.3 = 28.3 0.026 80-48 = 32 0.8 203 x 106 Apr 2900 16.1 = 24.9 0. 026 87-53 = 34 0.9 190 x 106 May 2218 14.1 = 21.8 0.029 90-63 = 27 0.8 132 x 106 Jun 1513 16.3 = 25.2 0.050 91-72 = 19 1.0 1 08 x 106 Jul 1248 16.3 = 25.2 0.061 94-76 = 18 1.1 102 x 1 06 Aug 1090 16.3 = 25.2 0.069 94-78 = 16 1.1 91 x 106 Sep 1080 16.3 = 25.2 0.070 90-72 = 18 1.3 102 x 106 Oct 1154 16.3 = 25.2 0.066 85-61 = 24 1.6 136 x 106 Nov 1701 17.7 = 27.4 0.048 83-53 = 30 1.4 185 x 106 Dec 2093 19.7 = 31.5 0.044 79-45 = 34 1.5 233 x 106 Annual 1910 17.3 = 26.8 0.042 91-59 = 32 1.3 193 x 106
( ) 260 12.4 = 19.2 0.222 85-61 = 24 5.3 104 x 106 (1) Extreme condition with 7-day, 10-year low river flow of 260 cfs and limited diffuser flow occurring with October river temperatures and October cooling tower blowdown temperatures that are exceeded only 50, 5, 1% of time respectively. October temperature differences were selected because this month would be most likely to contain the combination of low flow and high temperature difference.
Rev. 2, 12/81
LGS EROL TABLE 5.1-2 WEEKLY SCHUYLKILL RIVER WATER WITHDRAWALS DURING TWO UNIT SIMULATED FULL POWER GENERATION 1974-1978(t)
WITHDRAWALS WITHDRAWALS SCHUYLKILL RIVER WATER RIVER WATER FLOW INTAKE % OF FLOW FLOWS % OF FLOWS 1974-77 WITHDRAWAL 1974-1977 1926-75 1926-75 MONTH cfs cfs m__id Mfean Ma_ cfs mean Jan 3312 58.7 37.9 1.77 8.6 2067 2.84 Feb 2710 60.2 38.9 2.22 10.5 2464 2, 44 Mar 4008 65.3 42.2 1.63 5.9 3123 2.09 Apr 3244 66.9 43.2 2.06 4.0 2893 2.31 May 2434 46.8 30.2 1.92 4.6 2192 2.14 Jun 1554 34.6 22.4 2.23 4.1 1535 2.25 Jul 1533 23.0 14.9 1.50 4.4 1274 1.81 Auq 1179 22.9 14.8 1.94 4.2 1100 2.08 Sep 1439 22.1 14.3 1.54 5.0 1083 2.04 OctC2) 3232 29.9 19.3 0.93 3.1 995 3.01 Nov.(z) 2300 54.8 35.4 2.38 7.9 1651 3.32 Dec.(2) 2808 61.6 39.8 2.27 7.7 2046 3.01 Mean(2) 2445 45.3 29.3 1.85 10.5 18653 2.43
(')Based on weekly means of daily Schuylkill River flows and temperatures (Pottstown) and weekly means of hourly meteoroloqy from LGS Tower No. 1. Concentration factor equals 3.34 and drift equals 0.017 percent of circulatinq water and service water flows (1-1-74 to 9-31-78).
(2)Based on 1-1-74 throuqh 12-31-77.
(3)All months.
LGS EROL TABLE 5.1-3 (Page 1 of 2)
ENTRAINMENT LOSS OF MACROINVERTEBRATES AT LIMERICK GENERATING STATION MEAN DENSITY MONTHLY MEAN(&) MONTHLY MEANt2) PREDICTED MEAN DENSITY BIOMASS DRY RATE OF WATER VOLUME WATER PREDICTED BIOMASS (DRY STUDY NO./M3 -WT. /ms (mag) WITHDRAWAL WITHDRAWAL NUMBER WT. GRAMS)
DATE NEAR INTAKE NEAR INTAKE M34S M3 /DAY ENTRAINED/DA ENTRAINED/DAY 22 Mar 1.888 0.736 1.847 79790.4 150644.3 58.7 11 Apr 4.012 0.511 1.890 81648.0 32757.8 41.7 17 May 14.067 1.872 1.328 57369.6 807018.2 107.4 15 Jun 3.710 0.194 0.977 42206.4 156585.7 8.2 24 Jul 1.124 0.067 0.654 28252.8 31756.1 1.9 22 Aug 12.679 0.367 0.648 27993.6 354930.9 10.3 25 Sep 2.907 0.192 0.625 27000.0 78489.0 5.2 23 Oct 0.656 0.060 0.846 36547.2 23975.0 2.2 29 Nov 2.326 1.207 1.551 67003.2 155849.4 80.9 27 Dec 2.227 0.826 1.7543 75297.6 167687.8 62.2 1973 20 Mar 4.158 0.300 1.847 79790.4 331768.5 23.9 23 Apr 1.271 0.090 1.890 81648.0 103774.6 7.3 14 Jun 81.503 1.925 0.977 42206.4 3439948.2 81.2 7 Jul 4.659 0.214 0.654 28252.8 131629.8 6.0 13 Aug 30.606 0.674 0.648 27993.6 856772.1 18.9 10 Sep 15.940 0.489 0.625 27000.0 430380.0 13.2 15 Oct 0.549 0.038 0.846 36547.2 20064.4 1.4 15 Nov 0.8754 0.050 1.551 67003.2 58560.8 3.4 12 Dec 1. 193 0.280 1.743 75297.6 89830.0 21.1 1974 14 Mar 2.2542 0.357 1.847 79790.4 178890.1 28.5 19 Apr 2.605 0.281 1.890 81648.0 212693.0 22.9 17 May 73.5406 3.594 1.328 57369.6 4211272.9 206.2 154 Jun 20.125 0.485 0.977 42206.4 849403.8 41.2 12 Jul 26.606 0.571 0.654 28252.8 751694.0 16.1 8 Aug 2.698 0.121 0.648 27993.6 75526.7 3.4 10 Sep 1.196 0.067 0.625 27000.0 32292.0 1.8 11 Oct 0.307 0.040 0.846 36547.2 11220.0 1.5 8 Nov 0.029 0.004 1.551 67003.2 1943.1 0.3 6 Dec 3.930 0.374 1.743 75297.6 295919.6 28.2
LGS EROL TABLE 5.1-3 (Cont'd) (Page 2 of 2)
MEAN DENSITY MONTHLY MEAN(&) MONTHLY MEANCZ) PRED ICTED MEAN DENSITY BIOMASS DRY RATE OF WATER VOLUME WATER PREDICTED BIOMASS (DRY STUDY NO. tm3 WT./m 3 (mg) WITHDRAWAL WITHDRAWAL NUMBER WT. GRAMS)
DATE NEAR INTAKE NEAR IN-TKE m3/S m'/DAY ENTRAINED/DAY ENTRAINED/DfiY 1975 12 May 9.967 0.706 1.328 57369.6 571802.8 40.5 11 Jun 1.218 0.167 0.977 42206.4 51407.4 7.0 8 Jul 1.576 0. 104 0.654 28252.8 44526.4 2.9 5 Aug 3.160 0.077 0.648 27993.6 88459.8 2.2 2 Sep 5.145 0.257 0.625 27000.0 138915.0 6.9 15 Oct 0.093 0.019 0.846 36547.2 3398.9 0.7 (1)Monthly mean water withdrawal rate calculated from percent of river flows 1926-1975.
C')Monthly mean water withdrawal volume calculated from percent of river flows 1926-1975.
LGS EROL TABLE 5.1-4 (FPa I of 6)
PREDICTED ENTRAINMENT LOSS OF FISH EGGS AND LARVAE AT LIMERICK GENERATING STATION DURING THE 1975-76 SPAWNING, SEASON Mean 24-h Drift Density Estimated Within the Zone of Intake Withdrawal Rate Number Total River Flow Percent Flow Mean 24-h Riverwide Total Percent Drift Sample Date/Taxa Influence (no./m 3 ) (cms) {m 3 /24 h) Entrained (cms) {m3 /24 h} Withdrawn Drift Density (no./m 3 ) 24-h Drift Entrained 20 Hay Unidentified 0.0035 2.1 635 57.4 3.6 0.0015 7,438 8.5 Unidentified minnows 0.0174 [181,4001 3,156 (4,959,000) 0.0137 67,940 4.6 Vhite sucker 0.0738 13,390 0.0790 391P 800 3.4 Leponis app. 0.0017 308 0.0006 2,975 10.4 Tessellated darter 0.0035 635 0.0024 11,900 5.3 All 8 18,120 482,100 3.8 11 Jun Unidentified minnows 0.0057 2.1 1,034 51.8 4.1 0.0040 17,900 5.8 White sucker 0.0000 {181,4001 0 {4,476,000) 0.0007 3,133 0.0 Banded killifish 0.0012 218 0.0003 1,343 16.2 Lepomis spp. 0.0012 218 0.0008 3,581 6.1 White crappie 0.0126 2,286 0.0158 70,720 3.2 Tessellated darter 0.0034 617 0.0007 3,133 19.7 All a 4,373 99,810 4.4 24 Jun Fish eggs 0.0000 0.7 0 35.9 2.0 0.0064 19,850 0.0 Unidentified minnows 0.2182 ( 60,4801 13,200 03,102,000) 0.1756 5",700 2.4 Goldfish 0.0000 0 0.0023 7,135 0.0 Carp 0.0027 163 0.0008 2,485 6.6 Golden shiner 0.0013 79 0.0019 5,894 1.3 Quillback 0.0000 0 0.0004 1,241 0.0 Brown bullhead 0.0000 0 0.0002 620 0.0 Banded killifish 0.0013 79 0.0004 1,241 6.4 Lepoais spp. 0.0027 , 163 0.0019 5,894 2.8 Tessellated darter 0.0013 79 0.0008 2,482 3.2 All a 13,760 591,500 2.3
0 0 LGS EROL TABLE 5.1-4 (Cont'd) (Pare 2 of 6)
Mean 24-h Drift Density Estimated Within the Zone of1-31 Intake Withdrawal Rate Number Total River Flow Percent Flow Mean 24-h Riverwide Tocal Percent Dri.ft a as 1"4:1 - .B*,,
(*t_ (C-1, 1,,31/)A U1 E-.n 4-n*A Q
JT,,
I I. D-- a. a~U * ~c.a. & .~a-*r. &&, lbS*
08 Jul Fish eggs 0.0194 0.6 1,006 43.0 1.4 0.0069 25,630 3.9 Unidentified minnows 0.0850 { 51,840} 4,406 {3,715,000} 0.0733 272,300 1.6 Goldfish 0.0000 0 0.0011 4,086 0.0 Carp 0.0015 78 0.0007 2,601 3.0 Brown bullhead 0.0015 78 0.0016 5,944 1.3 Banded killifish 0.0015 78 0.0009 3,344 2.3 Rock bass 0.0015 78 0.0002 743 10.5 Lepomis app. 0.0015 78 0.0002 743 10.5 Alla 5,802 315,400 1.8 05 Aug Fish eggs 0.0027 0.7 163 59.4 1.2 0.0019 9,751 1.7 Unidentified 0.0000 { 60,480) 0 {5,132,000) 0.0003 1,540 0.0 Unidentified minnows 0.1744 10,550 0.1323 679,000 1.6 Goldfish 0.0027 163 0.0014 7,185 2.3 Carp 0.0054 326 0.0020 10,260 3.2 Golden shiner 0.0014 85 0.0014 7,185 1.2 Brown bullhead 0.0000 0 0.0003 1,540 0.0 Banded killifish 0.0014 85 0.0012 6,158 1.4 Lepomis spp. 0.0054 326 0.0088 45,160 0.7 Alla 11,700 767,779 1.5 19 Aug Unidentified 0.0000 0.6 0 35.9 1.7 0.0002 620 0.0 Unidentified minnows 0.0445 t 51,840) 2,307 (3,102,000) 0.0361 112,000 2.1 Goldfish 0.0000 0 0.0005 1,551 0.0 Golden shiner 0.0000 0 0.0002 620 0.0 Lepomis spp. 0.0000 0 0.0002 620 0.0 Alla 2,307 115,400 2.0 02 Sep Unidentified minnows 0.0056 0.6 290 31.1 1.9 0.0025 6,718 4.3 Goldfish 0.0000 ( 51,840) 0 {2,687,0001 0.0008 2,150 0.0 Alla 290 8,868 3.3
LGS EROL TABLE 5.1-4 (Cont'd) (Page 3 of 6)
Mean 24-h Drift Density Estimated Within the Zone of intake Withdravil Rate Number Total Riser Flow Percent Flow Mean 24-h Riverwids Total Percent Drift Sample Date/Taxs Influence (no./1) (cms) (M /24 h) Entrained (cms) (m /24 h) Withdrawn Drift Density (no./m ) 24-h Drift Entrained 1976 04 May Fish Eggs 0.0362 0.6 1,877 62.6 1.0 0.0179 56,800 3.3 Unidentified 0.0101 151,840] 524 15,408,000] 0.0055 2,974 17.6 Minnows Goldfish 0.2272 11.780 0.0309 167,100 7.0 Carp 0.0322 1,669 0.0038 20,550 8.1 White Sucker 0.0241 1,249 0.0098 53,000 2.4 Tessellated 0.0000 0 0.0008 4,326 0.0 darter Yellow Perch 0.0000 0 0.0004 2,163 0.0 Alla 15,200 250,100 6.1 18 Nay Fish Eggs 0.1554 0.6 8,056 75.6 0 0.8 0.4213 2.751,000 0.3 Unidentifted 0.0000 [51,8401 0 [6,531,000] 0.0004 2,612 0.0 Unident if ted 0.2904 15,050 0.0606 395,800 3.8 Minnows Goldfish 2.3027 119,400 0.1513 988,100 12.1 Carp 0.4949 25,660 0.0595 388.600 6.6 Golden shiner 0.0204 1.058 0.0010 6.531 16.2 White sucker 0.0164 850 0.0040 26,120 3.2 Creek 0.0000 0 0.0012 7,837 0.0 Chubsucker Lepomis app. 0.0082 425 0.0014 9,143 4.6 Crappie 0.0041 212 0.0009 5,878 3.6 Tessellated 0.0041 212 0.0028 18.290 1.2 darter Yellow Perch 0.0000 0 0.0004 2,612 0.0 Alla 162,900 1,852,000 8.8 01 June Fish Eggs 0.1966 0.6 10,190 49.8 1.2 0.3102 1,334,000 0.8 Unidenttfied 0.0386 151,840] 2,001 [4,303,0001 0.0028 12.050 16,6 Unidentified 0.2458 12.740 0.1832 788.300 1.6 Minnows Goldfish 8.5474 443. 100 0.6054 2,605.000 17.0
LGS EROL TABLE 5.1-4 (Cont'd) (Page 4 of 6)
Mean 24- Drift Density Estimated Within the Zone of intake Withdraw 1 Rate Number Total Ri~er Flow Percent Flow Mean 24-h Rivervids Total Percent Drift Sample Date/Taax Influence (no./Ia) (c) ,,/24 h) Entrained (ue)L (a /24 h) Withdrawn Drift Density (no./m ) 24-h Drift Entrained 01 June Carp 0.1229 6,371 0.0090 38,730 16.4 Golden shiner 0.0456 2,364 0.0028 12,050 19.6 White sucker 0.0035 181 0.0024 10,330 1.8 Ck. Chubsucker 0.0000 0 0.0009 3,873 0.0 Banded 0.0000 0 0.0004 1,721 0.0 Killifish Rock base 0.0000 0 0.0002 861 0.0 0.0000 0 0.0022 9,467 0.0 Tessel lated 0.0000 0 0.0013 5.594 0.0 darter Yellov Perch 0.0000, 0 0.0002 861 0.0 Al la 466,800 3,489,000 13.0 15 June Fish Eggs 0.0173 0.6 897 22.5 2.7 0.0284 55,210 1.6 Unidentified 0.7333 [51,8401 38,010 [1,944,0001 0.4876 947.900 4.0 Minnow Goldfish 1.3337 69,140 0.4151 807,000 8.6 Carp 0.1186 6,138 0.1515 294.500 2.1 Golden shiner 0.0866 4,489 0.0430 83,590 5.4 Banded 0.0000 0 0.0003 583 0.0 Killifish Rock base 0.0000 0 0.0003 583 0.0 0.1876 9,725 0.1085 210,900 4.6 Tessellated 0.0029 150 0.0026 5,054 3.0 darter All& 127,600 2,350,000 5.4 30 June Fish Eggs 0.0026 0.6 124 61.4 1.0 0.0273 144,800 0.1 0.2812 14,580 15.305,0001 0.1272 674,800 2.2 Unidentified [51,8401 minnows 0.0220 1,140 0.0131 69,500 1.6 Goldfish 0.0026 124 0.0034 18,040 0.7 Carp 0 0.0002 1,061 0.0 Golden shiner 0.0000 0 0.0002 1,061 0.0 White sucker 0.0000 Creek 0.0000 0 0.0002 1,061 0.0 Chubsucker
LCS EROL TABLE 5.1-4 (Cont'd) (Page 5 of 6)
Mean 24-h Drift Density Estimated Within the Zone of 3ntake Withdrau'l Rate Number Total Riser Flow Percent Flow mean 26-h Rliverwid Total Percent Drift Sam le Date/Tax. Influence ) -no.1.
(ems) (4M/24 h) Entrained (cume) (- /24 h) Withdravn Drift Deneity (no._1 ) 24-h Drift Entrained Catfishes 0.0049 254 0.0057 30,240 0.8 Sanded 0.0024 124 0.0010 5,305 2.3 Killifish LeIueis 0.0758 3,929 0.0152 80.650 4.9 Allor 20.150 881,700 2.3 13 July Fish Eggs 0.0023 0.6 119 47.0 1.3 0.0132 53,600 0.2 Unidentified 0. 1067 151,8401 5,531 (4,061,000) 0.0629 255,400 2.2 Minnows Goldfish 0.1180 6,117 0.0651 264,4600 2.3 Carp 0.0272 1,410 0.0317 128,700 1.1 Golden shiner 0.0023 119 0.0006 2,437 4.9 Catfish 0.0000 0 0.0006 2,437 0.0 Lepomisi 0.0340 1.762 0.0126 51,170 3.4 Arl" 14.940 704,500 2.1 27 July Fish Eggs 0.0000 0.6 0 20.4 2.9 0.0062 10,920 0.0 Unident if ied 0.1328 151.8401 6,884 11.762,0001 0.1254 221,000 3.1 Minnows Goldfish 0.1476 7,652 0.0266 46,870 16.3 Golden shiner 0.0059 306 0.0019 3,348 9.1 Sanded 0.0000 0 0.0006 1,057 0.0 KIllifish 0.0325 1,685 0.0149 26,250 6.4 16,530 298,500 5.5 12 August Fish Eggs 0.0000 0.6 0 37.1 1.6 0.0005 1.602 0.0 Unidentified 0.0538 151,8401 2,789 13,205,000) 0.0253 81,090 3.4 Minnows 0.0000 0 0.0002 641 0.0 Goldfish Banded 0.0000 0 0.0002 641 0.0 Killifish 0.0000 0 0.0003 962 0.0 Aeplli 2,789 83,330 3.3
LGS EROL TABLE 5.1-4 (Cont'd) (Page 6 of 6) nean zo-n £rurt uensity Estimated Within the Zone of intake
?nirl,,*nja (_fin~Im WithdrawlI Rate Number Total Ri3er Flow Percent Flow Nean 24-h Rliervidq Total Percent Drift lmeni ftiatap IY. 1-.mm -jfL4* S. R.# .. 4 - IIA'lL S 1 I4.J *
~~~Iflec tS I- . . ~ I N
~- 5
- U4 16A
.U~nB nJ8*6 W~& SWS a wI.dd W, ~
' V A-& %
- ~ W S V
USUC aA 25 August Fish Eggs 0.0026 0.6 135 23.0 2.6 0.0003 596 22.6 Unidentified 0.0497 151,840) 2,576 [1.987,0o0 0.0504 100,100 2.6 Uinnwm Goldfish 0.0471 2,442 0.0110 21,860 11.2 Ai il 5,018 122,000 4.1 "Rzaludes fish eags
LGS ERCL51-TABE TABLE S.1-5 IVERMAL TOLERANCE CF IMPORTANT FISHES OF THE SCHUYINILL RIVER NEAR LIMERICK GENERATING STATION U*FFE FINAL IOWER ACCLIMATION AVOICAhNCE PPIFERENCE AVCIDANCE SIZE/AGE TEMP. loci TEMP. 0oci 7IMP. (act TEMPo fo00 Muskellunqe Scott and Crossman Field Adult 25.6 (Ref 5.1-74)
Muskellunqe Laboratory Young 24.0 Ferguson (Ref 5.1-67)
Go ldfisb Laboratory Small 28.1 Fry (Ref 5.1-68)
Goldfish Laboratory Small 33.0 30.0 Roy and Johansen (Ref 5.1-73)
Goldfish Laboratory Adult 24.2 Reutter and Herdendorf (winter) (Pet5.1-71)
Goldfish Laboratory Adult 25.3 Peutter and Berdendorf (sprinq) (Ref 5.1-71)
Goldfish Laboratory Adult 27.0 Peutter and Berdendorf (summer) (Pef 5.1-71)
Goldfish Laboratory Adult 24.0 Peutter and Herdendorf (fall) (Ref 5.1-72)
Goldfish Reynolds and Covert Laboratory Medium 27.9 (Ref 5.1-7.21 Goldfish Laboratory Medium 20.6 Bile and Judy (Ref 5.1-69)
Goldfish Laboratory Medium 18.3 Cooper and Fuller (Ref 5.1-65)
Goldfish Laboratory Medium 18.9-21.1 BoraX and Tanner (Sef 5.1-70)
White sucker Adult 22.41 Reutter and Herdendcrf (Ref 5.1-72)
LGS EROL TABLE 5.1-6 (Page 1 of 2)
PREDICTED SEASONAL AVOIDANCE TEMPERATURES (F) OF IMPORTANT SCHUYLKILL RIVER FISHES UNDER TWO CONDITIONS OF LIMERICK GENERATING STATION OPERATION (I VALUES IN PARENTHESES GIVE 95% CONFIDENCE INTERVALS)(s,2)
WINTER SPRING LW~ MEDIA VMH ORMEDIANBG Extreme Blowdown Temp. (F) 55.3 59.4 65.6 62.0 73.9 87.2 Mean Blowdown Temp. (F) 53.9 56.4 60.5 58.0 66.8 82.1 River Temp. (F) 32.9 36.7 43.0 39.2 52.7 76.1 Species American shad 72.6(3.3) 82.8(2.2)
Muskellunge 84.7(3.9)
Swallowtail shiner 69.9(2.3) 72.6(2.1) 77.2(1.7) 74.4(1.9) 814.3(1.3) 101.2(1.7) spotfin shiner 59.2(2.1) 61.5(1.91 65.4(1.6) 63.1(1.8) 71.,4(1.2) 85.9(1.61 White sucker 56.8(3.8) 62.3(3.0) 59.0(3.5) 70.7(2.5)
Brown bullhead 89.6(3.8)
Banded killifish 68.9(3.8) 72.7(3.1) 70.14(3.5) 78.5(2.3) 92.6(3.0)
Redbreast sunfish 73.8(6.3) 90.14(2.8)
Pumpkinseed 64.8(3.2) 69.3(2.7) 66.6(3.0) 76.2(1.9) 92.9(2.0)
Largemouth bass 66.7(2.0) 70.6(1.7) 68.3(1.9) 76.6(1.3) 91.0(1.2)
0 (0 LGS EROL TABLE 5.1-6 (Cont'd) (Page 2 of 2)
SUMMER FALL W!MEDIA NON N MEDIAN HIGH Extreme Blowdown Temp. (F) 81.7 86.6 89.8 62.0 77.2 811.1 Mean Blowdown Temp. (F) 74.4 81.2 87.9 58.0 69.8 77.4 River Temp. (F) 161.1 74.7 85.1 39.2 57.2 68.9 Range of Acclimation Soecies Tuemnratures Tested American Shad 77.7(1.8) 82.1(2.0) 74.6(2.6) 79.6 (1.7) 52-82 Muskellunge 78.8(2.7) 84.0(3.6) 75.1(4.4) 81.1(2.51 57-79 Swallowtail shiner 92.8(1.2) 100.2(1.6) 71t.1 (1.9) 87.5(1.2) 96.0(1.4) 32-84 Spotfin shiner 78.7(1.2) 85.0(1.6) 63.1(1.8) 74.2(1.1) 81.41(1.3) 32-83 White sucker 80.8(3.51 89.7(5.1) 59.0(3.5) 74.6(2.7) 84.7(4.2) 34-75 Brown bullhead 81.7(2.7) 88.6(3.41) 76.84(4.4;) 84.7(2.5) 57-80 Banded killifish 85.5(2.1) 91.7(2.9) 70.41(3.5) 81.2(2.1) 88.2(2.41 36-82 Redbreast sunfish 82.1(3.7) 89.5(2.7) 77.0(5.2) 85.3(3.0) 50-84 Pumpkinseed 84.6(1.5) 91.9(1.9) 99.1(2.7) 66.6(3.0) 79.4(1.7) 87.8(1.6) 35-90 Largemouth bass 83.8(1.0) 90.2(1.1) 96.6(1.5) 68.3(1.9) 79.11(1.11 86.6(1.0) 34-93 (1)Avoidance temperatures predicted using the equation: Temperature = I
- a (Acclimation Temperature) vhera I and a are constants established by regression analysis.
()seasonal avoidance temperatures unavailable for American eel, goldfish, and tessellated darter.
LGS EROL TABLE 5.1-7 (Page I of 2)
PREDICTED SEASONAL PREFERENCE TEMPERATURES (F) OF IMPORTANT SCHUYLKILL RIVER FISHES UNDER TWO CONDITIONS OF LIMERICK GENERATING STATION OPERATION
(+/- VALUES IN PARENTHESES GIVE 95% CONFIDENCE INTERVALS) (1,2)
WINTER SPRING LOW MEDIAN HIGH LOW MEDIAN Extreme Blowdown Temp. (F) 55.3 59.4 65.6 62.0 73.9 87.2 Mean Blowdown Temp. (F) 53.9 56.4 60.5 58.0 66.8 82.1 River Temp. (F) 32.9 36.7 43.0 39.2 52.7 76.1 Species American shad 66.0(7.0) 70.3(4.7) 80.7(4.1)
Swallowtail shiner 55.2(5.3) 57.7(4.8) 61.9(3.9) 59.4(4.4) 68.4(3.0) 84.0(4.3)
Spotfin shiner 53.7(1.8) 56.0(1.6) 57.5(1.5)
Brown bullhead 51.8(7.8) 56.9(6.3) 53.8(7.2) 64.7(4.3) 83.5(4.5)
Redbreast sunfish 70.6(4.8) 82.8(3.4)
Pumpkinseed 67.3(3.6) 82.1(2.5)
Largemouth bass 63.5(3.2) 61.2(3.6) 69.2(2.4) 82.9 (1.8)
LGS EROL TABLE 5.1-7 (Cont'd) (Page 2 of 2)
SUMMER FALL W MEDI HIGH LQW MEDI B Extreme Blowdown Temp. (F) 81.7 86.6 89.8 62.0 77.2 84.1 Mean Blowdown Temp. (F) 74.4 81.2 87.9 58.0 69.8 77.4 River Temp. (F) 64.4 74.7 85.1 39.2 57.2 68.9 Range of Acclimation Species Temperatures Tested American Shad 75.5(3.0) 80.1(3.9) 72.3(3.8) 77.5(3.1) 42-82 Swallowtail shiner 76.2(3.1) 83.1(14.1) 59.1(4.11) 71.41(2.9) 79.2(3.4) 32-82 Spotfin shiner 57.5 (1.5) 32-40 Brown bullhead 74.1(3.2) 82.41(4.2) 53.8(7.2) 68.3(3.6) 77.7(3.41) 36-80 Redbreast sunfish 76.7(3.0) 82.0(3.2) 72.9(4.0) 79.0(2.8) 48-84 Pumpkinseed 74.7(2.2) 81.2(2.4) 70.2(2.9) 77.5(2.0) 47-83 Largemouth bass 76.1(1.7) 82.1(1.8) 88.2(2.5) 61.2(3.6) 71.8(2.0) 78.7(1.6) 37-90 (L)Preference temperatures predicted using the equation: Temperature = I + a (Acclimation temperature where I and a are constants established by regression analysis.
CR)Seasonal preference temperatures unavailable for American eel, muskellunge, goldfish, white sucker, banded killifish, and tessellated darter.
I.1 "
LGS EROL TABLE 5.1-8 SIMULATION OF WEEKLY PERKIOMEN CREEK WATER WITHDRAWALS DURING TWO UNIT, FULL POWER GENERATION, 1974-1978(t)
NO OF WEEKS PERKIOMEN CREEK INTAKE PERKIOMEN WATER AUGMENTA- WATER CREEK WITHDRAWALS AUGMENTA- FLOW INTAKE T ION WITHDRAWAL FLOWS % OF FLOWS INTAKE TION 1974-77 WITHDRAWAL FLOW % OF FLOW 1912-75 1912-75 MONTH OPERATED
- cfs, cfe OPERATED cfs( 3) cfs(4) MEAN ~MAX April 1 1 156 49.5 43.5 24.8 24.8 543 May 10 68 266 51.5 23.8 17.8 36.2 339 June 17 17 138 53.3 45.1 29.1 41.8 226 19.6 July 19 16 334 54.1 39.4 15.2 49.2 245 19.0 August 20 19 166 53.9 43.6 25.9 144.9 206 21.7 September 25 22 237 52.1 41.9 18.7 53.0 191 22.4 October 13 106 352 49.4 27.6 13.0 42.3 170 25.0 November 4 38 478 49.8 37.5 9.7 31.6 327 Mean( G) 249 52.5 38.6 18.2 53.0 208(7)
SumC G) 113 97
(')Based on weekly means of 1,) daily Perkiomen Creek flows (Graterford), 2,) daily Schuylkill River flows and temperature (Pottstown), and 3) hourly meteorology from LGS Tower No. 1. Concentration factor equals 3.34 and drift equals 0.017 percent of circulating water and service water flows (1-1-74 to 9-30-78).
(z)Total number of simulated weeks equals 247.
(3)Includes only those flows during times of intake operation.
(4)Means based on No. of weeks intake operated.
(S)Example calculation:
= (100)*(Intake Flow)/(Creek + Augmentation Flows)
% = (100) (49.5)/(156 + 43.5) = 24.8%
(C)1-1-74 thru 9-30-78.
(?)Months of June through October.
CS)Augmentation not operated during weeks when potential for flooding occurred.
- 1;
/,
LGS EROL Table 5.1-9 page 1 of 3 Predicted Entrainment Loss of Fish Larvae at the Graterford Intake, Perkiomen Creek, During the 1975 and 1976 Spawning Seasons Withdrawal Rate (cms) EstimatedTotal Number Augmented Stream FlowFlow24Wi Percent Total Percent Sample Date Taxa (m3I24-h)i Entrained (Cms) (mDr2i-h) Withdrawn Drift Entrained 19751 1 July Unidentified Fish 1.5 467 6.2 24.2 3261 14 Unidentified minnow (129,600) 3316 (535,700) 18510 18 Rockbass 607 5719 11 Lepomis spp. 5211 38390 14 2
Other 586 2402 24 All 10190 68280 15 29 July Unidentified fish 1.5 0 5.7 26.3 254.7 0 Unidentified minnow (129,600) 3781 (492,500) 34020 11 Leomis spp. 867 7868 11 3
Other 1371 2167 63 All 6019 46600 13 12 August Unidentified minnow 1.5 1895 3.9 38.5 4072 46~
Golden shiner (129,600) 0 (337,000) 96 0 Leoomis spp. 0 387 0 All 1895 4555 42 26 August Unidentified minnow 1.5 384 5.0 30.0 1257 30 Banded killifish (129,600) 0 (432,000) 161 0 All 384 1418 27 1976 22 April Carp 1.4 76090 7.0 20.0 253700 30 White sucker (120,960) 1083 (604*,oo) 13270 8 4
Other 3121 14203 22 281200 29 All 80290 281200 29
LGS EROL Table 5.1-9 (con't) page 2 of 3 Withdrawal Total Augmented Percent Total Percent Rate (cms) Estimated Stream Flow Flow 24-h Drift Rae(m)Number Witdrwn Dr-iDrt Sample Date laxa (m3/24-h) Entrained (cms) (M3124-) Withdrawn Drift Entrained 11 May Unidentified 1.4 9387 4.6 30.4 23320 40 5
Other (120,960) 328 (397,600) 592 55 All 9715 23910 41 25 May Unidentified minnow 1.4 1655 4.5 31.1 6897 24 Carp (120,960) 235 (386,600) 1957 12 White sucker 78 793 10 Rockbass 193 611 32 Other 6 234 366 64 All 2395 10620 23 8 June Unidentified minnow 1.5 1297 4.2 35.7 5566 23 Carp (129,600) 220 (366,200) 626 35 Levomis spp. 20345 64 7 28 345 8 Other All 1765 6882 26 22 June Unidentified minnow 1.5 16260 5.7 26.3 42550 38 Carp (129,600) 5389 (494,200) 15710 34 Yellow bullhead 795 12350 .6 Lepomis spp. 6033 39550 15 Other 8 2025 4073 50 All 30500 114200 27 6 July Unidentified minnow 1.5 4986 3.6 41.7 13610 37 Carp (129,600) 0 (306,800) 676 0 Yellow bullhead 267 1864 14 Lepomis spp. 1602 3358 48 All 6855 19510 35
LGS EROL Table 5.1-9 page 3 of 3 Withdrawal Total Augmented Percent Estimated Percent Total Rate (cms) Stream Flow 24-h Number Flow Drift Sample Date Taxa (m3124-h) Entrained (cms) (m3/24-h) Withdrawn Drift Entrained 20 July Unidentified minnow 1.5 4754 3.2 46.9 11960 40 Goldfish (129,600) 3346 (275,000) 6177 54 9 58 Other 618 1064 All 8718 19200 45 4 August Unidentified minnow 1.5 2511 3.1 48.4 6222 40 Carp (129,600) 715 (270,600) 2364 30 Leoomis spp. 1152 3879 30 All 4378 12460 35 17 August Unidentified minnow 1.5 604 53 28.3 5605 11 Carp (129,600) 0 (456,500) 157 0 Lenomis spp. 370 1854 20 All 974 7616 13 31 August Unidentified minnow 1.5 1457 3.2 46.9 6120 24 Goldfish (129,600) 0 (277,400) 520 0 All 1457 6640 22 Iln 1975 withdrawals from Perkiomen Creek would not have occurred until after June because consumptive use of the Schuylkill River was allowed (Section 2.4).
2 Taxa comprising less than 5%of total 24-h drift (carp, golden shiner, yellow bullhead, and brown bullhead combined).
3 Goldfish and carp.
4 Unidentified minnow, goldfish, Lepomis spp., tessellated darter, and shield darter.
5 Goldfish and tessellated darter.
6 Goldfish, Lepomis spp., and tessellated darter.
7 White sucker, creek chubsucker, rock bass, and smallmouth bass.
8 Goldfish, rock bass, and smallmouth bass.
9 Carp and Levomis spp.
LGS EROL TABLE 5.1-10 LIMERICK GENERATING STATION COOLING TOWER ANALYSIS DISTRIBUTION OF PHILADELPHIA EMSU(1) UPPER AIR SOUNDINGS NOVEMBER 1974 - OCTOBER 1975 237 TOTAL SOUNDINGS MONTH AM PM TOTAL JAN 20 19 39 FEB 18 17 3.5 MAR 21 15 36 APR 16 6 22 MAY 6 4 10 JUN 10 6 16 JUL 2 0 2 AUG 3 0 3 SEP 2 0 2 OCT 1 0 1 NOV 18 15 33 DEC 20 18 38 TOTAL 137 100 237 (1) Environmental Meteorological Support Unit
LGS EROL TABLE 5.1-11 LIMERICK GENERATING STATION COOLING TOUER ANALYSIS PERCENT FREQUENCY DISTRIBUTION OF PIUME RISE PERCENT FREOUENCY*
FINAL PLUME RISE IN METERS ABOVE PLANT GRADE
<500 501-1000 1001-1500 1500-2000 >2000 Limerick predicted rise (Based on all Philadelphia soundings) 0 65 23 10 2 Limerick predicted rise (based on Philadelphia winter morning soundings) 0 69 18 10 2 Amos Plant measured rise (winter morninqs only) 0 48 38 14 0 Winter is defined as December throuqh March. Both predicted and observed rises are for cases when the plume rose to an equilibrium height. Plumes which evaporated while rising were excluded from this portion of the analysis.
LGS EROL TABLE 5.1-12 LIMERICK GENERATING STATION COOLING TOWER ANALYSIS DIRECTIONAL DISTRIBUTION OF LONG AND EVAPORATED PLUMES Based on 237 Philadelphia EMSU( 1 ) Soundings DIRECTIONAL BEARING ALL SOUNDINGS WINTER MORNING SOUNDINGS LONG EVAPORATED LONG EVAPORATED S 7 8 3 3 ssW 5 4 3 1 SW 2 2 1 0 WSW 4 4 4 2 w 2 2 1 1 WNW 1 4 1 1 NW 2 3 0 1 NNW 2 4 1 1 N 7 6 3 0 NNE 10 6 2 0 NE 9 7 7 1 ENE 13 12 6 1 E 14 9 6 1 ESE 22 4 7 1 SE 26 9 15 0 SSE 18 9 3 2 TOTAL 144 93 63 16
(')Environmental Meteorological Support Unit Long plumes are those predicted to persist beyond two miles.
Winter is defined as December through March.
LGS EROL TABLE 5.1-13 LIMERICK GENERATING STATION DRIFT MODEL INPUT PARAMETERS BY MONTH MONTH MEAN PLUME HEIGHT NaCI CONC. IN CIRCULATING WATER (ft above grade) (mg/i)
JAN 3280 92.8 FEB 3280 107.7 MAR 3641 123.9 APR 4330 77.5 MAY 4330 120.6 JUN 4291 174.8 JUL 4291 90.6 AUG 4291 114.0 SEP 4034 101.7 OCT 3542 111.9 NOV 3542 113.3 DEC 3444 116.6
LGS EROL TABLE 5.1-14 L1MERICK GERATION STATION WEATHER STATION gO. 1 RELATIVE HUMIDITY DISMINUTION (%)
PERIOD OF RECORD: 1972 - 1976 REL. HUM.
%_ON FEBf W~ anf IX JUN jL AM fi= 2= pY DEC A14!L 90-100 26.4 20.9 20.7 16.6 31.7 37.7 33.3 37.9 43.2 37.5 19.? 23.5 29.4 80-89.9 8.9 8.1 7.6 7.9 12.2 14.0 13.8 13.6 15.1 12.7 10.4 11.7 11.4 70-79.9 12.0 10.3 8.5 10.4 11.9 11.3 12.2 10.7 10.6 11.2 15.5 15.4 11.6 60-69.9 18.8 14.0 15.9 14.4 11.9 12.7 12.9 11.0 10.1 11.3 21.5 19.3 14.3 50-59.9 20.0 21.6 19.0 17.1 11.9 12.4 13.4 14.1 10.1 11.8 20.9 18.3 15.7 40-49.9 10.7 16.5 16.2 18.2 13.1 8.4 12.0 10.0 8.2 10.5 10.5 10.3 12.0 30-39.9 2.9 7.1 10.4 13.6 6.3 3.2 2.5 2.5 2.5 4.2 1.2 1.4 4.8 20-29.9 0.3 1.5 1.7 2.1 1.1 .3 0 0.1 0.2 0.7 0.1 0.2 0.7
0 LGS EROL TABLE 5.1-15 LIM4LRICK GENERATING STATION WEATHER STATION MO. I WIND DIRECTION FREQUENCY DISTRIBUTION (11 PERIOD OF RECORD: 1972 - 1976 WIND DIRECTION SETOR JU3 ma As An mx m MZPAM I=E =~' MY PM~ RINDU 22.5 1.7 4.7 3.4 3.4 3.2 2.7 3.4 3.8 4.7 3.6 3.0 '4.1 3.4
'35.0 1.6 4. 4 4. 1 2.3 3.0 4.0 2.4 2.9 3.8 5.0 2.3 5.7 3.4 67.5 2.5 5.3 5.8 2.7 5. 4 4. 3 2.3 4.2 4.1 5.6 2.2 6.2 4. 2 90.0 6.8 5.2 9.4 4.7 6.7 6.6 3.6 4. 1 5.8 5.9 3.8 5.7 5.6 112.5 3.9 2.2 5.2 2. 9 5.4 4.1 2.9 2.8 4.0 2.8 4.1 3.1 3.6 135.0 4.9 2.8 4.4 2.0 4.4 6.2 3.3 2.6 2.6 2.7 3.8 3.7 3.6 157. 5 3.5 3.5 4.6 2.5 7.0 6.5 5.4 3.9 4.4 3.6 3.3 4.6 4.3 180.0 5.3 5.3 6.9 4.9 10.9 10.2 9.9 9.1 6.5 5.8 6.1 6.0 7.2 202.5 5.0 5.2 4.8 7.7 8.4 9.9 9.1 9.8 8.0 5.6 5.9 4e2 7.0 225.0 5.0 4.3 3.4 7.0 5.7 8.0 7. 2 7.2 4.9 5.0 5.7 4.0 5.7 247.5 4i. 5 5.0 3.1 6.1 4.1 6.6 7.6 7.0 5.0 5.3 6.1 3.5 5.4 270.0 10.9 9.1 6.1 8.6 7.5 9.3 11.2 7.9 8.5 9.7 12.7 10.3 9.5 292.5 19.4 18.2 16.8 18.0 13.1 10.2 14.3 15.9 14.5 14.4 18.9 18.8 16.1 315.0 15.4 13.0 12.9 15.1 8.8 5.5 8.8 9.2 11.2 11.5 12.0 11.9 11.2 337.5 5.2 6.0 4.6 6.6 2.9 3.6 4.1 4.8 5.9 7.4 5.6 4.6 5.2 360.0 4.4 5.9 4.6 5.6 3.6 2.2 4.5 4.9 5.9 6.1 4.6 3.6 4.7
LGS EROL TABLE 5.1-16 LIM4ERICK GENERATION STATION WEATHER STATION NO. 1 AVERAGE WIND SPEED BY DIRECTIONAL SECTOR()
PERIOD OF RECORD: 1972 - 1976 WIND SPEED fMONTHLYl IMI/HR)
WIND DIRECTION SECTOR JAN F MAR m mG mTN MZ~ haG SEPT M~ DM*g ANN1 22.5 8.2 10.3 9.6 11.5 8.6 8.4 6.5 8.0 8.1 7.8 10.6 8.3 8.3 45.0 5.9 9.8 9.8 9.6 8.9 9.5 6.4 6.1 8.9 8.5 8.0 9.1 8.8 67.5 6.4 10.1 9.6 11.0 9.0 8.5 5.3 7.3 9.1 9. 1 7.7 10.1 8.9 90.0 7.9 9.5 10.4 10.8 9.3 8.7 5.7 6.9 9.0 8.9 8.0 9.0 9.0 112.5 8.5 8.0 11.4 10.5 9.6 9.7 7.2 6.2 8.6 9.5 9.1 8.0 9.1 135.0 8.2 8.5 9.5 9.0 10.1 9.8 7.5 6.7 6.4 8.0 8.8 8.9 8.5 157.5 9.0 10.0 10.9 9.7 9.8 9.3 7.7 7.0 7.11 8.0 8.3 9.7 9.0 180.0 8.9 10.3 12.0 9.5 10.1 8.9 8.2 7.9 8.4 8.11 10.4 9.7 9.3 202.5 9.4 10.3 13.5 11.6 10.1 9.2 8.8 8.6 10.11 9.6 10.5 9.6 10.0 225.0 9.3 9.5 8.6 10.2 7.5 8.0 7.8 6.7 8.7 9.3 10.2 8.7 8.6 247.5 9.9 11.4 12.2 10.5 8.7 8.6 7.6 7.0 7.3 8.6 10.1 9.8 9.0 270.0 12.6 14.6 12.7 11.5 9.8 9.5 8.2 7.5 8.3 9.9 12.6 13.4 10.8 292.5 14.4 l4. 9 18.2 14.7 11.8 10.4 9.5 8.2 10.1 11.6 13.3 16.0 13.1 315.0 13.7 15.0 16.0 15.8 13.1 9.9 8.9 9.0 10.3 12.6 14.6 15.3 13.3 337.5 12.0 14.1 12.7 12.3 9.5 10.2 8.6 7.6 10.1 11.8 13.3 11.6 11.3 360.0 9.3 10.8 11.0 12.1 8.3 S.5 9.1t 7.5 9.4, 10.3 9.6 8.6 9.7
LGS EPCL TABLE 5.1-17 LIMERICK GENERATION STATION UEATHER STATION NC. I MONTHLY AND ANNUAL MEAN TEMPERATURES (OF)
PERIOD OF PECCED 1972 - 1976 MEAN January 31.6 February 30.2 March 40.8 April 51.2 May 60.3 June 69.0 July 73.2 Auqust 72.2 September 64.5 October 53.4 November 44.5 December 34.5 Annual 51.8 Annual 51.8
LGS EROL TABLE 5.1-18 LIMERICK GENERATING STATION NaCI ANNUAL DEPOSITION AS A FUNCTION OF THE DISTANCE FROM THE TOWER (lb/acre/yr)
DEP. SECTOR 1/2 MILE I MILE 2 MILES 22.5 4.3 2.4 0.8 45.0 4.3 2.5 0.8 57.5 3.9 2.1 0.7 90.0 5.5 3.3 1.1 112.5 6.8 4.5 1.5 135.0 5.1 3.9 1.3 157.5 2.6 1.7 0.6 180.0 3.2 1.8 0.6 202.5 2.5 1.5 0.5 225.0 2.8 2.1 0.7 247.5 3.3 2.6 0.9 270.0 4.3 2.4 0.8 292.5 2.7 1.5 0.5 315.0 2.9 1.7 0.6 337.5 3.3 1.9 0.6 360.0 4.9 2.9 0.9
LGS EZOL TABLE 5.1-19 LINEKCR GENERATING STATION MONTHLY NaCi DEPOSITION AT TH~E SITE BOUNDARY (lt/acre)
DZPOSITION TO mmII 2W 41A. LZa 22.,0 112, 135.0 157.5 180.0 o02 225.0 .257 270.0 292, 315.0 337.5 360.0 Jan 0.28 0.28 .0.23 0.39 0.48 0.46 0. 18 0.26 0.10 0.17 0.22 0.47 0.25 0.33 0.19 0.26 Feb 0.34 0.28 0.22 0.26 0.53 0.39 0.18 0.31 0.25 0.24 0.29 0.33 0.20 0.22 0.19 0.29 mar 0.21 0.29 0.14 0.29 0.26 0.43 0.20 0.26 0.22 0.27 0.39 0.53 0.29 0.29 0.25 0.334 Apr 0.17 0.20 0.15 0.20 0.27 0.22 0.13 0.13 0.08 0.07 0.07 0.12 0 . 07 0.08 0.07 0. 14 may 0.32 0.40 0.22 0.33 0.44 0.26 0.13 0.22 0.19 0.14 0.24 0.28 0.26 0.19 0.32 0.40 Jun 0.75 0.75 0.52 0.63 0.62 0.49 0.15 0.18 0.22 0.21 0.34 0.51 0.27 0.41 0.47 0.67 0.334 0.34 0.39 0.51 0.51 0.39 0.15 0.15 0.21 0.19 0.17 0.25 0.15 0.15 0.25 0.42 Jul 0.62 0.57 0.62 0.84 0.55 0.27 0.38 0.21 0.29 0.29 0.32 0.24 0.24 0.29 0.51 fiUq 0.62 0.33 0.31 0.45 0.65 0.72 0.60 0.26 0.32 0.29 0.20 0.20 0.27 0.24 0.27 0.32 0.37 Sep 0.34 0.39 0.67 0.73 0.55 0.33 0.41 0.31 0.35 0.36 0.36 0.17 0.26 0.28 0.41 Oct 0.36 0.40 0.58 0.65 0. 43 0.16 0.32 0.19 0.17 0.17 0.30 0.28 0.29 0.26 0.32 Nov 0.31 0.28 0.23 0.410 0.60 0.37 0.20 0.30 0.33 0.37 0.34 0.41 0.29 0.30 0.28 0.37 Dec 0.10 0.30 Annual (lb/acre/yr) 4.3 4.4 3.9 5.6 6.7 5.1 2.3 3.2 2.6 2.7 3.1 4.2 2.7 3.0 3.2 4.6 Distance (Yards) 867 067 867 833 833 833 1100 833 833 967 933 933 867 833 967 967 867 867 867 833 833 833 1100 833 933 967 933 933 867 833 967 967
LGS Zl!OL TABLE 5.1-20 LIMERICK GENERATING STATION MONTHLY NaCI DEPOSITION RATE AT 1/2-MIME DISTANCE (It/acre)
, DEP*SITION SECTOR a013TH ",I.. M~a.Q IM2L 22,_q 112,~ 1350 157.5 100,~ 202L, 225, 247. 270.0 292.5 315~.0 337.5 360.0 Jan .28 .28 .23 .38 .48 .46 .20 .25 .10 .18 .23 .68 .25 .33 .20 .30 re .34 .28 .22 .28 .53 .39 .20 .31 .25 .25 .31 .34 .20 .22 .20 .31 Hat .21 .28 .16 .28 .25 .42 .21 .25 .21 .28 .39 .53 .28 .28 .25 .35 Apr .17 .19 .14 '.19 .26 .21 .14 .12 .07 .07 .07 .12 .07 .07 .07 .14 May .32 .39 .21 .32 .62 .25 .16 i.21 .18 .14 .25 .28 .25 .18 .32 .42 Jun .73 .73 .31 .60 .60 .47 .17 .17 .21 .21 .34 .51 .26 .39 .47 .77 Jul .34 .36 .40 .52 .52 .40 .18 .15 .21 .21 .18 .27 .13 .15 .27 .46 Aucz .62 .62 .58 .62 1.06 .55 .31 .38 .21 .31 .31 .34 .24 .24 .31 .58 Sep .33 .31 .45 .66 .71 .59 .28 .31 .28 .21 .21 .28 .24 .26 .33 .38 Oct .37 .34 .60 .66 .71 .56 .37 .60 .30 .40 .60 .60 .17 .24 .30 .46 Nov .31 .28 .60 .58 .64 .63 .18 .31 .18 .18 .18 .31 .28 .28 .28 .34 Dee .30 .30 .23 .60 .60 .37 .23 .30 .33 .60 .40 .63 .30 .30 .30 .40
IGS EROL TABLE 5.1-21 LIM4ERICK GENERATING STATIO1q MONTHLY NaCl DEPCSITION RATE AT I-MIlE DISTANCE (Lb/acre)
_____DEPOSITjION SECT0R W211 AM §17 2290 112.5 135.0 157.5 100., 202.5 225.0 247, 27.0iQ 292.. 3.5l.a 33.5! 360.0 Jan .16 .16 .11 .26 .38 .33 .13 .13 .06 .06 .09 .22 .11 .18 .11 .17 Feb .18 .16 .16 .21 .42 .30 .15 .19 .16 .16 .20 .19 .09 .10 .13 .18 Mar .13 .16 .09 .19 .20 .30 .15 .17 .13 .17 .25 .35 .18 .18 .17 .22 Apr .12 .13 .11 .13 .20 .16 .10 .09 .05 .04 .014 .0o .05 .04 .05 .10 May .214 .22 .13 .22 .31 .18 .09 .12 .11 .10 .18 .21 .16 .13 .20 .30 Jun .116 .4411 .33 .111 .412 .28 .11 .12 .14 .14 .23 .33 .19 .27 .31 .50 Jul .24 .20 .23 .31 .314 .23 .11 .11 .11 .11 .08 .13 .09 .11 .16 .27 Auq .32 .30 .22 .23 .52 .29 .17 .18 .13 .16 .16 .16 .12 .10 .111 .32 Sep .20 .17 .18 .32 .45 .38 .19 .19 .15 .12 .12 .17 .15 .15 .17 .19 Oct .20 .19 .20 .38 .412 .33 .23 .20 .15 .18 .18 .22 .10 .16 .16 .23 Nov .18 .16 .21 .34 .38 .27 .141 .14 .10 .09 .09 .16 .15 .14 .114 .20 Dec .16 .16 .12 .27 ,42 .27 .15 .14 .16 .18 .18 .22 .10 .13 .15 .22
LGS EROL TABLE 5.1-22 LIMERICK GENERATING STATION DRIFT WATER DEPOSITION AT THE SITE BOUNDARY (Inches)
DEPOSITION SECTION BMWh 45.0 67.5 102.5 135.0 157.5 2205 247.0 27Q.0 2079;. 360.
0.003 Jan 0.008 0.008 0.006 0.011 0.013 0.013 0.005 0.007 0.005 0.006 0.013 0.007 0.009 0.005 0.008 0.008 Feb 0.011 0.009 0.007 0. 009 0.017 0.012 0.006 0.010 0.008 0.009 0.010. O. 006 0.007 0.006 0.009 0.007 Mar 0.007 0.010 0.005 0.010 0.009 0.014 0.007 0.009 0.009 0.013 0.018 0.010 0.010 0.008 0.011 Apr 0.007 0.007 0.005 0.008 0.010 0.008 0.005 0.005 0.003 0. 003 0.003 0.005 0.003 0.003 0.003 0.005 May 0.012 0.015 0.008 0.012 0.017 0.010 0.005 0.008 0.007 0.005 0.009 0.011 0.010 0.007 0.012 0.015 Jun 0.025 0.025 0.0 17 0.021 0.021 0.016 0.005 0.006 0.007 0.007 0.011 0.017 0.009 0.014 0.016 0.025 Jul 0.017 0.017 0.019 0.026 0.025 0.020 0.*008 0.007 0.010 0.009 0.008 0.012 0.007 0.008 0.013 0.021 Auq 0.o024 0.024 0.023 0.025 0.042 0.022 0.011 0.015 0.009 0.012 0.012 0.013 0.009 0.010 0.012 0.022 Sep 0.012 0.011 0.016 0.023 0.025 0.020 0.009 0.011 0.010 0.007 0.007 0.010 0.009 0.009 0.011 0.013 Oct 0.012 0.011 0.013 0. 022 0.024 0.018 0.011 0.014 0.010 0.012 0.012 0.012 0.006 0.009 0.009 0.014 Nov 0.012 0.010 0.015 0.022 0.024 0.016 0.006 0.012 0.007 0.006 0.006 0.011 0.010 0.011 0.010 0.012 Dec 0.013 0.013 0.010 0.017 0.025 0.016 0.009 0.013 0.014 0.016 0.016 0.018 0.013 0.013 0.012 0.016 Annual 0.153 0.160 0.144 0.205 0.253 0.187 0.086 0.116 0.096 0.098 0.113 0.149 0.098 0.108 0.116 0.171 Distance (yards) 867 867 867 833 833 833 1100 833 833 967 933 933 867 833 967 967
-x .-
oj
.- *J Ji. iSCLE edl~r "4waft "
I. 3900 CUBIC YARD3 7D BE PLR£EED
- 2. PLAmT COOADINArTES ARE 5ma WN. Am CoNivErps T7 PENNSYL WANIA STATE COORDINATES:
N. PLANT COOrD .325,870.00 N. PENN 3TAT COORD.
E PLANT COORD 2,,9, 78d,0
- E. PENN STATE CO*Ra
- 3. DATUM IS MEAN SEA /CEVLI Offt V X, AREA OF INITIAL DILUTION FULLY MIXED FROM RIVER BOTTOM TO
'WATER SURFACE.
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT INITIAL DILUTION AREA OF DIFFUSER DISCHARGE REV. 2, 12/81
I
/
- S S -- I UNIT 2 I
D ~~ -'..
TURBINE - REACTOR ENCLOSURE COMPLEX
...... V....
je LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTkL REPORIT COOLING TOWER LOCATIONS' FIGURE 5.1-2
8c I-m m
Co w
r-a O0 3
2 C
m am a, 0 m m
-I 2 M z- C, m m z &
ocz 0
I- m 0 1 10 100 1000 10,000 DISTANCE FROM COOLING TOWER RIM (ft.)
f
LGS EROL CHAPTER 6 EFFLUENT AND ENVIRONMENTAL MEASUREMENTS AND MONITORING PROGRAMS TABLE OF CONTENTS Section Title 6.1 APPLICANT'S PREOPERATIONAL ENVIRONMENTAL PROGRAMS 6.1.1 Surface Waters 6.1.1.1 Physical and Chemical Parameters 6.1.1.2 Ecological Parameters 6.1.1.2.1 Schuylkill River 6.1.1.2.2 Perkiomen Creek 6.1.1.2.3 East Branch Perkiomen Creek 6.1.1.2.4 Glossary 6.1.2 Ground Water 6.1.2.1 Physical.and Chemical Parameters 6.1.2.2 Models 6.1.3 Air 6.1.3.1 Meteorology 6.1.3.1.1 Meteorological Measurement System 6.1.3.1.2 Measurements and Instrumentation 6.1.3.1.3 Calibration and Maintenance Procedures 6.1.3.1.4 Data Analysis Procedure 6.1.3.2 Models 6.1.4 Land 6.1.4.1 Geology and Soil 6.1.4.2 Land Use and Demographic Surveys 6.1.4.2.1 Land Use 6.1.4.2.2 Demography 6.1.4.3 Ecological Parameters 6.1.4.3.1 Flora 6.1.4.3.2 Waterfowl 6.1.4.3.3 Breeding Birds 6.1.4.3.4 Winter Birds 6.1.4.3.5 Migratory Birds 6.1.5 Radiological Monitoring 6.1.5.1 Preliminary Survey Study 6.1.5.2 Preoperational Radiological Monitoring 6.1.5.2.1 Air Particulates 6.1.5.2.2 Direct Radiation 6.1.5.2.3 Surface and Drinking Water 6.1.5.2.4 Groundwater 6.1.5.2.5 Shoreline Sediment 6.1.5.2.6 Milk 6.1.5.2.7 Fish 6-i Rev. 15, 08/83
LGS EROL CHAPTER 6 TABLE OF CONTENTS (Cont'd)
Section Title 6.1.5.2.8 Food Products 6.1.6 References 6.2 APPLICANT'S PROPOSED OPERATIONAL MONITORING PROGRAM 6.2.1 Nonradiological Monitoring Programs 6.2.2 Radiological Monitoring Programs 6.3 RELATED ENVIRONMENTAL MEASUREMENT AND MONITORING PROGRAMS 6.4 PREOPERATIONAL ENVIRONMENTAL RADIOLOGICAL MONITORING DATA 6-ii Rev. 15, 08/83
LGS EROL CHAPTER 6 TABLES Table No. Title 6.1-1 Limerick Water Quality Program Summary 6.1-2 Limerick Water Quality Program Parameters, Procedures, and References 6.1-3 Schuylkill River Benthic Macroinvertebrate Program Summary 6.1-4 Schuylkill River Larval Fish Drift and Trap Program Summary 6.1-5 Schuylkill River Larval Fish Drift and Trap Program Sample 6.1-6 Data Used to Calculate Mean Densities for Specific Analyses of Schuylkill River Larval Fish Drift 6.1-7 Schuylkill River Larval Fish Push Net Program Summary 6.1-8 Schuylkill River Seine Program Summary 6.1-9 Schuylkill River Small Fish Population Estimate Program Summary 6.1-10 Schuylkill River Large Fish Estimate Program Summary 6.1-11 Schuylkill River Large Fish Catch per Unit Effort Program Study 6.1-12 Schuylkill River Age and Growth. Program Summary 6.1-13 Schuylkill River Vincent Pool Trap Net Program Summary 6.1-14 Perkiomen and East Branch Perkiomen Creek Benthic Macroinvertebrate Program Summary 6.1-15 Perkiomen and East Branch Perkiomen Creek Macroinvertebrate Drift Program Summary 6.1-16 Perkiomen Creek Larval Fish Drift and Trap Program Summary 6.1-17 Perkiomen Creek Larval Fish Drift and Trap Program Sample Design 6iii
LGS EROL CHAPTER 6 TABLES (Cont'd)
Table No. Title 6.1-18 Perkiomen Creek Drift and Trap Data Utilized to Calculate Mean Densities for Specific Analysis 6.1-19 Perkiomen Creek Seine Program Summary 6.1-20 Perkiomen Creek Small Fish Population Estimate Program Summary 6.1-21 Perkiomen Creek' Large Fish Population Estimate Program Summary 6.1-22 Perkiomen Creek Age and Growth Program Summary 6.1-23 East Branch Perkiomen Creek Periphyton Program Summary 6.1-24 East Branch Perkiomen Creek Larval Fish Drift Program Summary 6.1-25 East Branch Perkiomen Creek Larval Fish Drift Data Utilized to Calculate Mean Densities for Specific Analysis 6.1-26 East Branch Perkiomen Creek Seine-Program Summary 6.1-27 East Branch Perkiomen Creek Large Fish Population Estimate Program Summary 6.1-28 East Branch Perkiomen Creek Age and Growth Program Summary 6.1-29 Chemical Analysis of Ground Water in the Brunswick Lithofacies in Montgomery County, Pennsylvania Chemical Analysis of Ground Water from Wells in the 6.1-30 Brunswick Lithofacies at the Limerick Project Site 6.1-31 Meteorological Instrument Elevations 6.1-32 Meteorological Sensor and System Specifications and Accuracies 6.1-33 Percent of Hours with Calm Wind 6.1-34 Preliminary Survey Study Summary of Samples Analyzed 6iv
LGS EROL CHAPTER 6 TABLES (Cont'd)
Table No. Title 6.1-35 Preliminary Survey Study (1971-1977), Radiological Environmental Monitoring Stations 6.1-36 Preliminary Survey Study Results - Air Particulate Samples 6.1-37 Preliminary Survey Study Results - Precipitation Samples 6.1-38 Preliminary Survey Study Results - Well Water Samples 6.1-39 Preliminary Survey Study Results - Surface Water Samples 6.1-40 Preliminary Survey Study Results - Silt Samples 6.1-41 Preliminary Survey Study Results - Milk Samples 6.1-42 Preliminary Survey Study Results - Strontium 89 and 90 Analyses 6.1-43 Preliminary Survey Study Results - Summary of TLD Results for all Stations 6.1-44 Preliminary Survey Study Results - Summary of Gamma Spectrometry by Mediatype 6.1-45 Preoperational Radiological Environmental Monitoring Program 6.1-46 Preoperational Radiological Environmental Monitoring Program Station Locations 6.1-47 Detection Capabilities for Environmental Sample Analyses 6.1-48 Environmental Sampling and Measuring Equipment 6v Rev. 7, 08/82
LGS EROL CHAPTER 6 FIGURES Figure No. Title 6.1-1 Water Sample Collection Sites 6.1-2 Aquatic Chemistry Stations 6.1-3 Main Effort to Ecological Study on Schuylkill River, 10 km Stretch 6.1-4 Periphyton Artificial Substrate Assembly 6.1-5 Macrophyte Study Area on the Schuylkill River 6.1-6 Benthic Macroinvertebrate Cylinder Sampler 6.1-7 The Macroinvertebrate Drift Sampler 6.1-8 Larval Fish Drift Sample Sites 6.1-9 Larval Fish Drift Collection Net 6.1-10 Larval Fish Push Net 6.1-11 Large Fish Population, and Age and Growth Sampling Locations 6.1-12 Largest Fish Catch per Unit Effort Sampling Locations 6.1-13 Perkiomen Creek Study Area 6.1-14 Portable Invertebrate Box Sampler 6.1-15 Larval Fish Drift Net Sites 6.1-16 Larval Fish Plywood Sampler 6.1-17 Larval Fish Drift Sample Sites 6.1-18 Ground Water Users 6.1-19 Location and Relationships Between Various Wind and Temperature Instruments 6.1-20 Location and Relationships Between Various Wind and Temperature Instruments 6vi
LGS EROL CHAPTER 6 FIGURES (Cont'd)
Figure No. Title 6.1-21 LGS Flora Study Area
- 6. 1-22 Water Fowl Study Area 6.1-23 Locations of Stations Sampled during the Preliminary Study Period, within 1 mile 6.1-24 Locations of Stations Sampled during the Preliminary Study Period, within 1 mile 6.1-25 Locations of Stations Sampled during the Preliminary Study Period, 1 to 5 miles 6.1-26 Locations of Stations Sampled during the Preliminary Study Period, 1 to 5 miles Locations of Stations Sampled during the 6.1-27 Preliminary Study PzerieA, beyond 5 miles 6.1-28 Environmental Sampling Stations, Site Boundary I 6.1-29 Environmental Sampling Stations, Intermediate I
Distance 6.1-30 Environmental Sampling Stations, Distant Locations 6vi i Rev. 7, 08/82
SECTION 6.1.1, SURFACE WATERS LGS EROL CHAPTER 6 EFFLUENT AND ENVIRONMENTAL MEASUREMENTS AND MONITORING PROGRAMS 6.1 APPLICANT'S PREOPERATIONAL ENVIRONMENTAL PROGRAMS The Applicant has conducted several environmental monitoring programs in the vicinity of the Limerick Generating Station to collect baseline data before operation of the station.
Procedural details of the techniques, instrumentation and scheduling used in each program are set forth in this chapter and/or other chapters of this report.
6.1.1 SURFACE WATERS 6.1.1.1 Physical and Chemical Parameters Water for plant operation will be taken from the Schuylkill River, Perkiomen Creek, East Branch Perkiomen Creek, and Delaware River. Water taken into the plant for condenser cooling will be concentrated by evaporation and discharged into the Schuylkill.
The aquatic chemistry program was initiated in May 1974 to provide water quality, aquatic chemistry, physical, hydrologic, and meteorologic information on all the streams potentially affected by plant and water diversion operations.
The objectives of the program were to (1) determine existing water quality and the controlling factors in the Schuylkill River, Perkiomen Creek, East Branch Perkiomen Creek, and Delaware River, (2) establish a preoperational data base to be used for assessing possible effects of plant operation and diversion, and (3) provide water quality data for aquatic ecological programs.
All water samples were collected in polyethylene bottles as mid-channel subsurface grabs. Samples were collected once every two weeks on the same day at S73880, S77040, S77140, S77660, P14390, P18700, E2800, E22880, E26700, E32300, and A11263 (Table 6.1-1 and Figures 6.1-1 and 2). In addition a daily sample was taken at S77660 to provide a detailed record of physical and chemical fluctuations of the Schuylkill. These data complimented biological programs and detected short-term fluctuations in water quality caused by upstream activity.
Analytical procedures for water quality parameters represented the best available methodologies and were approved by state and federal regulatory agencies. The parameters measured, procedures used, and references are given in Table 6.1-2.
6.1-1
LGS EROL W Measured constituents of the carbonate cycle were calcium, alkalinity, pH, hardness, free carbon dioxide, and total organic carbon. Elements of the carbonate cycle were used in interpreting effects of water quality on stream biota. The measured constituent of the sulfur cycle was sulfate, an essential biotic micronutrient. Sodium, potassium, chloride, magnesium, calcium, iron, and manganese were the major anions and cations measured. These ions, and sulfate and carbonate, control calcium carbonate precipitation in the cooling towers and corrosion properties of the cooling water system. Total phosphate-phosphorus and ortho phosphate-phosphorus were the measured constituents of the phosphorus cycle. Phosphorus is an essential plant nutrient and frequently plays a major role in regulating primary production. Ammonia, nitrite, and nitrate were the measured constituents of the nitrogen cycle. The nitrogen cycle is of interest because of the role of nitrogenous substances as essential plant nutrients. In addition ammonia is toxic to aquatic biota, and chlorination of water containing high ammonia concentrations results in the formation of chloramines, which are more toxic than ammonia alone (synergism). Trace elements measured were arsenic, boron, cadmium, chromium, cobalt, copper, lead, mercury, nickel, selenium, and zinc. These elements are important because of their toxicity to biota.
- Dissolved oxygen, temperature, suspended solids, dissolved solids, specific conductance, turbidity, and flow were the measured physical parameters. These parameters aided in describing stream quality by depicting loading characteristics, load composition, and temperature and dissolved gas regimes.
These parameters were also used in conjunction with biological data.
6.1.1.2 Ecological Parameters The programs described in this section provided information for predicting operational effects, and initiated a reference framework for detecting and assessing operational effects of LGS on the Schuylkill River, Perkiomen Creek, and East Branch Perkiomen Creek. The aquatic biota of these lotic systems is diverse and productive (Section 2.2) and was studied by the Applicant's consultants from 1970 through 1978. Biotic components studied included phytoplankton, periphyton, macrophytes, macroinvertebrates, and fish. The basic objective of the studies was to describe, for the principal aquatic habitats, the species composition, abundance, and natural variation of resident biota.
6.1-2
LGS EROL 6.1.1.2.1 Schuylkill River A description of the Schuylkill River and surrounding watershed is given in Chapter 2. LGS will impact the river through intake operation and blowdown discharge. The main effort of ecological study focused on a 10-km stretch of river which extended from meter 72120 (Vincent Pool Dam, the only impoundment in the study area) to meter 81750 (just above the Firestone Tire and Rubber Company plant) (Figure 6.1-3). This reach included both potentially unaffected (upriver of plant) and affected (downriver of plant) sections. The river in this reach was about 100 m wide, low gradient (0.4-0.5 m/km), averaged 53 m 3 /s discharge, and was 95% run habitat, 0.6-1.2 m deep, with a gravel-rubble bottom. Water velocity was usually between 0.1 and 0.7 m/s.
Riffle and pool habitats each accounted for about 2.5% of the study area with some backwater areas also present. Limerick Island was the only island in the study area. It was wooded, about 300 m long and 100 m wide, and divided the river into two channels near the proposed plant intake and discharge structures.
Occasional sampling was conducted outside the primary study area.
Sample stations on the Schuylkill River were designated by the letter 'S' followed by a number which indicated distance in meters from the mouth of the river. Where sample stations included several meters of stream, site numbers designated the downstream end of the station.
6.1.1.2.1.1 Phytoplankton Phytoplankton samples were collected at one station (S77720) located at the downriver end of a long run, 15 m from the Chester County shore. Samples were obtained weekly by two methods. In 1973, 100 1 of water were poured through a No. 20 (80 micron) mesh plankton net suspended in the water. This method was discontinued because of (1) distortion of plankton during sampling, (2) net clogging, and (3) passage of smaller algal forms through the net. In 1974 subsurface grab samples were collected with a 0.95-1 sampling bottle. Samples were stored live in 1973, but preserved in alcohol-formalin in 1974. Samples were concentrated by sedimentation for a minimum of 72 hours8.333333e-4 days <br />0.02 hours <br />1.190476e-4 weeks <br />2.7396e-5 months <br />.
The supernatant was siphoned off to leave 100 ml of concentrated phytoplankton. This sample was agitated and a subsample was removed and placed in a 0.1-ml Palmer-Maloney nannoplankton counting chamber. The entire chamber was examined under 400X magnification. Identifications were made to genus.
Phytoplankton was analyzed based on taxonomic composition and density.
6.1-3
LGS EROL 6.1.1.2.1.2 Periphyton Two stations were sampled for periphyton. Station S77580 is upstream from the plant intake and discharge structures. The second station (S77260) was located on the Chester County side of the river opposite the discharge.
Plexiglas slides (artificial substrates) were used to sample periphyton. The Plexiglas plates (each with an exposed area of 1.0 dm2 ) were attached to an aluminum supporting rack by pinch clamps (Figure 6.1-4). The entire assembly was held in place on the river bottom so that colonizing organisms were subjected to the same environmental influence as the natural substrate.
Plates were held in a vertical position and oriented with ends facing into the current. Vertical positioning reduced silt accumulation, a factor known to affect colonization rates.
Sampling was conducted twice per month, May through October, because periphyton standing crops can change rapidly with changes in river flow.
Periphyton was field-scraped from four plates, and another four clean plates were set. Both stations were sampled on the same day. Samples were returned to the laboratory for processing. Of the four plates removed three were used to determine community ash-free dry weight (mg/dmi), a measure of organic content, using procedures outlined by the American Public Health Association (Ref 6.1-1). The fourth plate was examined under magnification to determine the taxonomic composition and dominant algae of the sample. Identification was based on Patrick and Reimer (Ref 6.1-2), Weber (Ref 6.1-3), and Hansmann (Ref 6.1-4).
Reference diatom slides were prepared in 1973.
Parameters studied were standing crop biomass and taxonomic composition. Standing crop biomass is the weight (mg/dmi) of all taxa combined for each sample. Taxonomic composition is a listing of the taxa present. Lists were compiled for each site each year.
6.1.1.2.1.3 Macrophytes Macrophytes may be affected by changes in water quality near the discharge. The study area encompassed about 3.6 km of the Schuylkill River (S75400-S79030) in the vicinity of LGS (Figure 6.1-5). In 1974 macrophytes were surveyed by boat and mapped.
In 1977 macrophytes were sampled utilizing aerial oblique photographs taken monthly from May through October to document growth and dieback of the macrophyte community. Photographs were taken from an aircraft flying at about 150 m elevation.
Overlapping photographs were taken of each shore to provide a 6.1-4
LGS EROL continuous record of the entire study area. Natural color and infrared photographs were taken simultaneously. All flights were made on clear days, near noon when reflection is reduced and light penetrates to a maximum depth. Following each photographic flight an in-river survey of the macrophytes was made from a boat. This provided species identification and general distribution for comparison with the aerial photographs.
In the laboratory, a map of aquatic macrophyte beds was produced for each taxon using both aerial photographs and in-river observations. Identifications were based on Fassett (Ref 6.1-5).
Representative specimens of flowering stalks, leaves, stems, and roots were pressed and mounted for inclusion in a voucher collection.
Parameters utilized to study macrophytes included taxonomic composition, relative qualitative abundance, and coverage.
Taxonomic (species) composition of a community is a listing of the species present. Relative qualitative abundance was based on in-river observations, and was reported as abundant, common, uncommon, or rare for each species. These categories were defined as follows: abundant -- species which occurred in large numbers throughout the study area, common -- species which occurred in moderate numbers, uncommon -- species which occurred only in a few discrete locations, and rare -- species represented by only a few plants at very few locations in the study area.
Coverage was the areal extent of macrophyte growth, expressed as surface area (M2 ) and percent of total area occupied. These data were measured directly from aerial photographs for each important species, if possible, or for all species combined upriver and downriver of LGS.
6.1.1.2.1.4 Benthic Macroinvertebrates The location and description of sample stations are given in Table 6.1-3. All sampling locations (one upriver of LGS and three downriver) are in run-rubble habitat, which predominates in the Schuylkill study area.
Benthic samples were taken monthly with a natural-substrate colonization sampler (Figure 6.1-6) similar to the buried cylinder sampler described by Coleman and Hynes (Ref 6.1-6). The sampler consisted of permanent outer and removable inner "pots" (inner pot dimensions: 19 cm high, 27.9 cm in diameter), both with sides constructed of perforated sheet aluminum, allowing organisms to colonize the sampler from the top and laterally within the substrate (the bottom of both pots was unperforated sheet aluminum). This sampler (1) reduced the effects of substrate differences, (2) provided samples of known volume, (3) accurately reflected changes in numbers and biomass of benthos 6.1-5
LGS EROL due to fluctuations in natural conditions, and (4) penetrated the hyporheos and hence collected organisms missed by other types of benthic samplers.
Each station contained eight samplers, situated as pairs 1.2 m apart on a transect which began about 10 m from shore and extended 12 m toward midriver. Four cylinders (four sample units = 1 sample), one from each consecutive pair (initially randomly selected), were collected and processed from each station each month. Thus each sampler remained in the river-bed for approximately 2 months (allowing maximum colonization) before it was processed and reset.
After samples were returned to the laboratory, the rocks, nylon bags, and inner pots were thoroughly hand-scrubbed and rinsed with water. Contents were then wet-sieved through a 0.35 mm mesh screen and the residue was preserved in isopropanol.
Invertebrates were hand-sorted, counted, and preserved in vials with 70% isopropanol. All macroinvertebrates from each sample unit were identified and counted. Midges (Chironomidae) and sludge-worms (Tubificidae) were often subsampled.
Total biomass was determined for each sample unit. All organisms from each sample unit were dried at 600C in a drying oven for 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br />, cooled at room temperature, and weighed on a Mettler balance to the nearest 0.1 mg. Shells of mollusks were dissolved in HCO prior to weighing.
Identification of macroinvertebrates to species was desirable, but not always possible, because taxonomy for immature stages of some groups has not been developed. Therefore this program occasionally treated organisms at the genus or higher level.
Whenever a new taxon (the lowest taxonomic level to which an organism was identified) was identified, it was added to the species list and to a reference collection. In this way specimens could be reidentified as updated keys became available, and the data base amended if necessary. Keys used for identification were listed beside their respective taxon on the species list (Table 2.2-12). Where keys were either unavailable or incomplete, letter designators were sometimes used to denote apparently 'different members of the same genus (e.g., Hydropsyche sp. 'A', 'B', 'C', etc). When identification was questionable, the specimen was sent to a specialist for verification.
The benthic macroinvertebrate community was characterized using the following parameters: (1) taxonomic composition, (2) total taxa per sample, (3) relative abundance, and (4) density.
Taxonomic composition of a community is a listing of the taxa present. Taxonomic lists were compiled for each site each year.
Total taxa per sample is an indication of benthic species richness. Counts of total taxa per sample were based on number of taxa, not species, because not all organisms were identified 6.1-6
LGS EROL to species level. Relative abundance is the total number of individuals of a species (taxa) expressed as a percentage of the total number of individuals of all species. A listing of taxa by relative abundance indicated which taxa dominated (i.e.,
accounted for a large percentage) the community. Density (standing crop) is the number or weight/M2 of selected or total taxa for each sample each month.
6.1.1.2.1.5 Macroinvertebrate Drift Macroinvertebrate drift was studied from 1972 through 1975 to identify the kinds and quantities of macroinvertebrates that may be entrained. Drift samples were collected monthly at station S77560, located in the immediate vicinity of the intake site, approximately 25 m from the Montgomery County shore. Depth ranged from about 0.5 to 1.5 m, and current velocities ranged from 0.12 to 0.72 m/s at times of sampling. The habitat type was run/rubble, the dominant habitat in the study area. The macroinvertebrate drift sampler (Figure 6.1-7) consisted of an aluminum frame (32 x 48 cm), to which was attached a tapering net of 0.47-mm mesh. To increase filtration efficiency the frame was fitted anteriorly with a mouth-reducing rectangular Plexiglas enclosure, which tapered to a 7.6 x 30.5-cm (1972) or 10 x 46.4-cm (1973-1975) opening. The net was 1.2 m long. An aluminum ring, threaded on the inside to accommodate a 500-ml plastic sample bottle, was attached to the end. Two eyebolts fastened to each vertical side of the frame allowed placement of the sampler over steel rods placed in the substrate. On each sampling date two samplers were set sidde by side, about 1 m apart. Each sampler projected slightly above the water surface to collect surface drift. Samplers were placed in the river for a 60 or 30-minute period every two hours for each 24-hour study period. Samples were preserved in the field with 95%
isopropanol. In the laboratory, these samples were processed and identified in the same manner as benthos samples (section 6.1.1.2.1.4). Every two hours, water samples for dissolved oxygen determinations were collected and water and air temperatures taken near the drift nets. Mean current velocity was calculated at least once during each study by taking readings at the bottom, middle, and top of the opening of each sampler with a Gurley current meter (Model 625F).
Macroinvertebrate drift was studied using the following parameters: (1) taxonomic composition, (2) relative abundance, and (3) numeric and biomass densities. Drift densities (numbers or biomass per unit volume of water) were determined for each study by dividing the total number of organisms collected by the actual volume of water sampled (velocity x area of net opening x time sampled). An organism was considered dominant in 6.1-7
LGS EROL drift if it accounted for 1% or more of the total number of organisms collected during the year.
6.1.1.2.1.6 Fish
- a. Larval Fish Drift and Trap Larval fish drift was studied in 1974, 1975 and 1976 to identify the kinds and quantities of larvae that may be entrained, and to assess the impact of estimated losses.
Time and duration of fish spawning was also identified.
In this Section the term "larvae" includes juveniles
<21 mm, unless otherwise stated. Larval fish drift was sampled at S77560. In 1974 samples were collected from four sublocations at S77560 whereas six locations were sampled in 1975 and 1976 (Figure 6.1-8). In 1975 traps were used to sample movement in shallow low-velocity areas near shore.
Drift collections were made with cone-shaped nets (0.471-mm mesh), attached to 30.5 x 45.4-cm aluminum frames, fitted with clear Plexiglas aprons which tapered forward to delimit a 10 x 46-cm opening (Figure 6.1-9).
The sampler was held stationary by metal rods placed in the substrate. Wooden larval fish traps were 49.4 cm wide by 30.4 cm high, and fitted with two 1.5-m wings made of 0.5-mm mesh netting (Figure 6.1-9). Each trap had a removable front screen (mesh, 0.5 mm) used to guide trap contents into the catch net.
Drift and trap samples were taken over 24-hour periods throughout the spawning season. In 1974 drift samplers were set at 1000, 1200, 2200, and 2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br /> for one hour. In 1975 and 1976 they were usually set for one hour every even hour throughout the 24-hour period; sample interval varied according to water conditions.
Number and location of nets varied among years (Tables 6.1-4 and 5). Trap nets were retrieved and reset every four hours in each 1975 study.
Water velocity through drift samplers was measured with a Gurley current meter (Model 625F). Replicate measurements were taken at the bottom, middle, and top of each sampler's mouth. Water velocities inside and at the stream side of each trap were estimated with a cork and watch. The depth of water passing through each sampler was also measured. Water and air temperatures, and dissolved oxygen were determined each time the nets were set.
6.1-8
LGS EROL Samples were preserved in 5% formalin with rose bengal stain, and returned to the laboratory for sorting.
Larvae were identified, counted, and measured to the nearest millimeter total length. All specimens were retained in labeled vials containing 5% formalin.
Identifications were made to the lowest practicable taxonomic category, in many cases genus and species.
Lack of published material on larval fish identification precluded all specimens being identified to species level. Identifications were based on Fish (Ref 6.1-7),
Mansueti and Hardy (Ref 6.1-8), May and Gasaway (Ref 6.1-9), Snyder (Ref 6.1-10), and Lippson and Moran (Ref 6.1-11). Reference specimens supplied by the Muddy Run Ecological Laboratory (Drumore, PA) and larvae reared from known parentage in the Pottstown Laboratory were also used.
An effort was made to determine whether larvae in the drift were living or dead. On 20 May and 11 and 24 June 1975, randomly chosen samples were field-sorted in a white enamel pan immediately after capture. Larvae that moved or were not opaque were considered alive. Living and dead fish were preserved in separate containers, and later identified and measured as previously described.
Larval fish drift was described as the mean density (no./m 3 ) of total drift and of important taxa. Density data were used to indicate quantitative abundance, relative abundance, spatial and temporal distribution, and time and duration of spawning.
Mean drift densities for all taxa combined and important taxa were calculated by dividing the sum of larvae collected in selected drift nets by the sum of water volume sampled by those nets. Volume was determined using average velocity, submerged cross-sectional area of the net, and length of sample period. Because the number of nets and sampling duration varied, it was necessary to select data from common nets and sample times when comparing annual results. Further information on data used to calculate mean larval densities for specific analyses is presented in Table 6.1-6.
Because a horizontal gradient in larval densities was detected, only data from those nets that sampled within or nearest to the zone of intake influence were used to calculate entrainment estimates. The zone of intake influence was calculated for each sample day by the formula:
6.1-9
LGS EROL W
W=TQ (6.1-1)
R where: W = zone of influence width I
W = total stream width T
o = mean river discharge from appropriate 7-day R period (7-day mean discharge values were given in the PECo flow simulation of 21 May 1978).
Q = mean pumping rate (mu) from the 7-day period.
P (mu = mean 7-day intake flow given in the PECo flow simulation of 21 May 1978).
Estimates of entrainment, total drift, and percent entrainment were calculated as follows:
- 1. Entrainment during the 24-hour sample period D = (i )(F ) (6.2-2)
E I I where: D = no. of larvae entrained during the 24-hour E sample period
= 24-hour mean larval density (no./m 3 ) at those I nets within or nearest to the zone of intake influence (W)
I F = total water withdrawn (m 3 ) by the intake I during the 24-hour period (appropriate mu value x 86400 s)
- 2. Total drift past intake location during 24-hour sample period(1975)
D = ( )(F ) (6.2-3)
T T T 6.1-10
LGS EROL where: D = total drift (total no. larvae drifting T past the intake during the 24-hour sample period) 3
= river-wide 24-hour mean larval density (no./m )
T F = volume of water passing intake location T during the 24-hour sample period (daily flow (mi/s) x 86400 s)
- 3. Percent entrainment during the 24-hour sample period D
D =E (6.2-4)
T where: D = percent of larvae drifting by the intake
% during the 24-hour sample period which would have been entrained D = total no. of larvae drifting past the intake T during the 24-hour sample period D = no. of larvae entrained during 24-hour sample E period Time of spawning for some species was approximated by back-calculating from the development stage of larvae at the time of collection (usually 1-2 weeks for yolk-sac larvae). Peak spawning period was approximated from the date of greatest drift density of each taxon. Data on time and duration of spawning provided information on when and for how long eggs and larvae of important species would be subject to entrainment, and aided in quantifying the potential entrainment impact.
Trap catches were recorded as catch (total taxa and important taxa) per sample period, and were used to describe the quantitative and relative abundance of larvae in the shoreline areas adjacent to the proposed intake location.
- b. Larval Fish Push Net Three sites (S78973, S78432, S77970) upstream of the proposed discharge structure, and ten sites downstream (S77550, S77485, S77320, S77230, S77161, S76970, S76840, 6.1-11
LGS EROL S76794, S76632, S75781) were sampled. Habitat features of sites are summarized in Table 6.1-7.
The push net consisted of a 0.47-mm mesh net, fastened to an aluminum frame (0.5 by 0.2 m), attached to an aluminum pole (Figure 6.1-10). Stations were sampled between 1000 and 1400 hours0.0162 days <br />0.389 hours <br />0.00231 weeks <br />5.327e-4 months <br /> once per week throughout summer, except when river flow was high and turbid. At each station, one 10-m sweep was made slightly off the bottom while walking downstream approximately 2 m from shore. Consistent effort was maintained among sample sites and dates. After each sweep the net contents were washed into a 4 liter jar, preserved immediately with 5%
formalin, and stained with rose bengal. Water temperature and dissolved oxygen were determined at each collection site.
Samples were returned to the laboratory, sorted by trained technicians, and specimens stored in labeled vials with 5% formalin. Larval fish were identified to the lowest practicable taxonomic category (usually species), counted, and measured to the nearest millimeter total length. Life stage (yolk-sac, early and late post-larval, juvenile) was noted.
Identifications were made using Fish (Ref 6.1-7),
Mansueti and Hardy (Ref 6.1-8), May and Gasaway (Ref 6.1-9), Snyder (Ref 6.1-10), and Lippson and Moran (Ref 6.1-11) and a reference collection.
Parameters calculated from push-net collections included catch per effort of minnows, Lepomis spp., goldfish, banded killifish, and all taxa combined, and total seasonal catch of all identifiable taxa. Catch per effort is defined as catch per day, the number of individuals of a selected taxon collected from one sample site during one sample day. This parameter provided a qualitative measure of spawning success and recruitment potential exhibited by larval fish stocks.
Total seasonal catch, a listing by taxa of all collected specimens, was used as an indicator of interspecies relative abundance or community structure.
- c. Seine Fishes efficiently sampled by seine include cyprinids (minnows) and young-of-year pan and sport species. A total of 11 sites, five upriver of LGS (S81750, S78900, S78460, S77960, S77240) and six downriver (S77220, S77010, S76840, S76820, S76310, 575730) were sampled.
6.1-12
LGS EROL Salient habitat features of each site are presented in Table 6.1-8.
Fishes were collected with a 3.2-mm mesh seine, 2.4 m long by 1.2 m deep. The netting generally retained fish larger than 16-mm fork length (FL). All stations were sampled monthly throughout the year. Approximately 30 m of shoreline at each site was seined. To minimize effects of constant fishing pressure on populations, the catch at each site was occasionally subsampled in the field. The seine was divided into four sections and net quadrants from which fishes to be collected were randomly selected for each haul. Subsampling rates were held constant within site. Adult pan and sport fish in selected quadrants were identified, measured to the nearest 5 mm interval FL, and released.. All other fish in selected quadrants were preserved.
Prior to collection of fishes, water temperature, pH, and dissolved oxygen concentration were determined for each collection. These measurements were recorded in the field, as were duration of each seine haul, relative water level, weather conditions, water clarity, and pertinent remarks or observations.
Collected specimens were field-preserved in 10%
formalin, rinsed in water, and stored in 40%
isopropanol. All fish were identified to species, counted, and measured to the nearest 5-mm interval FL.
The total weight of each species was determined.
Taxonomic determinations were made using standard fish references (Blair et al (Ref 6.1-12), Eddy (Ref 6.1-13),
Bailey et al (Ref 6.1-14), and occasionally outside experts. In cases of questionable identification, specimens were preserved and returned to the laboratory for verification. A voucher collection consisting of juveniles and adults of each species collected from the study area was maintained in the laboratory.
Seine data were summarized as to quantitative abundance, number of species per sample, and relative abundance.
Quantitative abundance was estimated from total catch per sample for all species combined, swallowtail shiner, spotfin shiner, redbreast sunfish, pumpkinseed, total catch minus swallowtail shiner, and total catch minus spotfin shiner. Various physiochemical parameters were measured concurrent with collection of biological data, for possible correlation with fish abundance and distribution.
6.1-13
LGS EROL
- d. Small Fish Population Estimate This program described the small fish (age 0 sunfish, young of the sucker and catfish families, killifish, darters, and minnows) community in the vicinity of LGS.
Ten sites up and downriver of LGS were sampled in 1973.
In 1974 four new sites were added on the basis of habitat similarity and appropriate water depth to ensure electrofishing success. Three sites were added in 1975, one upriver of the proposed intake, one downriver, and one at the intake area. Sites are described and located in Table 6.1-9. All sites were sampled annually in the fall, when age 0 sunfish were of gear-catchable size and spawning had usually been completed.
Sampling was performed in shore sections (sites) isolated from the river with block nets (3.2 mm2 mesh) to prevent the escape of fish. Fish were collected with electrofishing apparatus, consisting of a portable Georator (500 W, 2.2 A, 230 V dc, with full-wave rectification) mounted in a 2.4-m aluminum boat on wheels, two hand-held anodes, and a cathode. Three consecutive sample runs were made in each site. A three-man crew fished the site by wading upriver; two men shocked and netted fish, while the third pulled the boat and controlled the Georator. During a run the enclosed area was carefully electrofished and all stunned fish (excluding minnows in 1974) were collected, regardless of size. Each run was considered a single unit of effort. The shocking crew attempted to maintain constant effort among runs, although time varied somewhat depending on the number of fish and difficulty of cover.
Fish larger than 70 mm FL were identified to species, measured to the nearest millimeter, weighed to the nearest gram, and released outside the enclosed area.
Fish less than 71 mm collected in each run were weighed as a unit, preserved for five days in 10% formalin, rinsed for two days in water, and stored in 40%
isopropanol. Stored specimens were later identified, measured, and reweighed individually to the nearest 0.1 g, except in 1973 when weights were taken by 5-mm intervals. Scale samples by 5-mm intervals were obtained from the sunfish, except in 1973. These were subsequently aged, and used in conjunction with length-frequency distributions to ascertain the maximum length age 0 sunfish had attained by time of capture.
6.1-14
LGS EROL Small fish were monitored by site using the following parameters: (1) estimated number and biomass of age 0 redbreast sunfish, green sunfish, and pumpkinseed, (2) length-weight relationship of age 0 sunfish, and (3) relative abundance (percent of total catch) of all species, regardless of size. Estimated number and biomass were regarded as gross measures of year-class strength and productivity, while length-weight relationship was used as an indication of condition (robustness) of young sunfish.
Population estimates of age 0 sunfish within each collection site were made by the maximum likelihood method of Zippen (Ref 6.1-15, 6.1-16). The model is based on depletion of the population by constant sampling effort. A modification of this method by Junge and Libosvarsky (Ref 6.1-17), cited by Seber (Ref 6.1-18) for three-sample cases provided the two principal formulas used to calculate these estimates:
" = 6X2-3XY-Y2+Y(Y2+6XY_3X2)1/2 (6.1-5) 18(X-Y)
= 3X-Y-(y2+6XY_3X2)1/2 (6.1-6) 2X where: N = estimated population size X = 2 ni+n 2 (nI = catch from first run; n2 - catch from second run)
Y nln2÷+n-ý (n3 = catch from third run) estimated probability of capture Standard errors ofl'andjý were calculated by two formulas from Zippen (Ref 6.1-15, 16) using similar notation to above:
(1 SE] =-Y) Y y- [R] _y)(kR)z2 (6.
SE ['j = 2________
(6.1-8) 6.1-15
LGS EROL where: SE[I] = standard error of population estimate k - number of sampling runs (k=3)
SE[r] = standard error of probability of capture estimate " = (I-$)
The estimate, plus and minus two standard errors, provides 90% confidence limits for populations of 50 to 200 fish, and 95% limits for populations of greater than 200 fish.
Sunfish older than age 0 were not included in the estimates. Some of these fish might have escaped from the collection site while nets were being hung, and numbers collected probably do not reflect their actual abundance within the site.
Biomass estimates of young sunfish were calculated by the formula:
- Wt(O)/Y (6.1-9) where: = estimated weight N = estimated population size Wt - total weight of fish taken in three runs Y = total catch from three runs Maximum and minimum values of biomass were estimated by replacing 1ý in the above formula with the upper and lower limits of I, respectively.
- e. Large Fish Population Estimate Fish longer than 70 mm FL studied in this program included juveniles and adults of the sucker, freshwater catfish, sunfish families, and goldfish. Sampling was conducted at four locations: one upriver of LGS, S79400 (Firestone); one near the proposed intake, S77240 (Limerick A); one downriver of the proposed discharge, S76440 (Limerick B); and one in Vincent Pool, S74365 (Table 6.1-10, Figure 6.1-11).
Fish were collected at night from a 5.2 m aluminum boat equipped with a bow shocking cage. Four electrodes, each composed of two 120-cm long elements of 1-cm 6.1-16
LGS EROL diameter flexible aluminum conduit, formed the anode array, which hung from a T-boom off the bow. Two cathode arrays, each composed of three 122-cm long elements of 1.2-cm diameter flexible aluminum conduit, were hung from the gunwales. A generator supplied 230 V ac to a variable voltage pulsator, which transformed it to dc and supplied it to the anode array at approximately 5 A at 40 Hz, with a pulse width of 25%.
Sites were sampled in the summer every other year, to provide at least two estimates per generation for even the shortest-lived species of interest. Each station was divided into longitudinal electrofishing zones to facilitate effective coverage of all habitat types.
Each zone was sampled in a downstream direction at a speed slightly faster than water velocity. This prevented released fish from becoming recaptured or trapped in the electrofishing field. Shocked fish were collected by scap net, placed in a livebox, identified to species, measured to the nearest millimeter FL, examined for marks from previous samples, marked with a specific half fin-clip, and released in the zone where they were captured. Air and water temperature, dissolved oxygen, and pH were routinely measured at the beginning of each sample night.
After population estimate sampling was concluded, one night was spent at each site to collect fish for establishing length-weight relationships. Fish collected for this purpose were identified to species, measured to the nearest millimeter FL, and weighed to the nearest gram.
Catch data from each site were used to calculate relative abundance (percent of catch of all species sampled) and estimate the standing crop (number and biomass) of five important species: white sucker, brown bullhead, redbreast sunfish, pumpkinseed, and goldfish.
These species comprised the bulk of the large fish standing crop (number and biomass) in the river.
Estimates of standing crop number (population size) were made by the Schumacher-Eschmeyer technique. Schnabel estimates of population size were calculated to assess the accuracy of the Schumacher-Eschmeyer model.
To avoid estimate bias caused by differential catchability among lengths, catch statistics were tabulated by FL interval. The first interval was 5 mm (71-75 mm); subsequent intervals were 25 mm. The variance test for homogeneity of the binomial distribution (Snedecor and Cochran, Ref 6.1-19) was used 6.1-17
LGS EROL to detect differences in the recapture-to-catch ratio between size classes, an indicator of differential catchability. When significant test statistics were obtained, estimates for appropriate size groups were calculated separately.
Schumacher-Eschmeyer estimates were calculated using formulae presented by Schumacher and Eschmeyer (Ref 6.1-20), and modified by DeLury (Ref 6.1-21) and Ricker (Ref 6.1-22). Usinq the notation:
Rt = estimate of the number of fish present in the population at time 't' Mt = total number of marked fish at large at the start of the 't'th day (number previously marked minus any removals)
Ct = total sample taken on the 't'th day Rt - number of recaptures in the sample Ct pt - Rt ct m = number of samples the formulae were:
Population Estimate I Z(Mt Rt)
(6.1-10)
Vn2) at Variance S2J(1)
Ct Mt 2 (6.1-11)
Standard Error Y2 2
SE (6.1-12) 6.1-18
LGS EROL Confidence Limits 1 t(m _ 2) SE (6.1-13)
Nt [()][E(]
Confidence limits of it were found by inverting those for I 1't.
The inverse form of the original Schumacher-Eschmeyer formula was used because it was more accurate to compute confidence limits for the more symmetrical distribution of 1/' (Ref 6.1-21). However this method yields asymmetrical confidence limits.
The Schumacher-Eschmeyer model is based on a weighted linear regression of the proportion of marked fish in each sample on the total number of fish previously marked. The best indication of a valid estimate is a highly linear regression line which passes through the origin (Ref 6.1-18). To test the validity of estimates, weighted linear regressions were calculated for each estimate. If the resulting line had a correlation coefficient significantly different from zero and a Y-intercept not significantly different from zero, the estimate was considered valid.
Schnabel population estimates (Ref 6.1-23) were calculated from the formula E(Mt Ct) (6.1-14)
N ERt E
the notation being the same as that given earlier.
When rRt exceeds 50, R is considered to be normally distributed (Ref 6.1-24), and 90% confidence limits are placed around the estimate by E(Mt Ct) (6.1-15)
ER +/- 1.645 Rt When ERt is less than 50, R is considered to be a Poisson variable (Ref 6.1-24), and 90% confidence limits are placed around the estimate using tabled confidence 6.1-19
LGS EROL limits for the expectation of a Poisson variable (Ref 6.1-25).
Length-weight relationships were established, and biomass was estimated for each species by the following calculations:
(1) weight of species A in length interval i =
% of species A population ideal weight of a fish collected in x estimate of x in length interval i, length interval species A obtained from length-i weight regression (2) biomass of species A = r weights of each length interval
- f. Large Fish Catch per Unit Effort Fish larger than 50-mm FL studied in this program included American eel, members of the sucker, freshwater catfish and sunfish families, and goldfish. This program provided seasonal data on the abundance and condition of these fishes.
Sampling was conducted at five locations (Figure 6.1-12): one upriver, S79310 (Firestone); one near the proposed intake, S77640 (Limerick A); two downriver of the proposed discharge structure, S76940 (Limerick B) and 576440 (Limerick C); and one in Vincent Pool, S74365. Each site was located within a large fish population estimate site. Habitat features are presented in Table 6.1-11.
For a description of the electrofishing gear used in this program, refer to Section 6.1.1.2.1.6e. All sites were fished once per month throughout the year, the minimum frequency that provided sufficient data for analysis of seasonal variation in abundance of important species. Each site was divided into 100-m sections, which were further divided into five electrofishing zones parallel to shore, across the river.
Fish were collected during daylight. The boat was moved downstream through each electrofishing zone at a speed slightly faster than water velocity. This minimized the likelihood of fish being recaptured or becoming trapped in the electrofishing field. Shocked fish were collected by scap net, placed in an aerated live-box, identified to species (Section 6.1.1.2.1.6c), measured 6.1-20
LGS EROL (FL to nearest 5-mm length interval), examined for parasites or symptoms of disease, and released. At least once each season a subsample of goldfish, white sucker, brown bullhead, redbreast sunfish, and pumpkinseed was selected, and each individual measured to the nearest millimeter FL and weighed to the nearest gram. The time required to fish each zone within a section was recorded to the nearest minute.
Water temperature, dissolved oxygen concentration, and pH were routinely measured at the beginning of each sample. At the conclusion of sampling, current velocity at both the upriver and downriver boundary of each electrofishing zone was determined with a Gurley current meter (model 625F).
Parameters used to seasonally monitor selected fishes larger than 50 mm FL included catch per unit effort (C/f) of important species, species composition, length-weight relationships of important species, and various physiochemical measurements. Catch per effort (C/f) values for each month were calculated within each 100-mi section of a site as catch per minute of electrofishing.
Mean site values of C/f were determined for important species. Three 100-m sections were sampled at Firestone and Limerick C, whereas four 100-m sections were sampled at Limerick A, Limerick B, and Vincent. Therefore, in calculating means, one 100-m section was randomly (random-number table) eliminated from each month's data for Limerick A, Limerick B and Vincent, so that means for all stations were based on three C/f values. Catch per unit effort of American eel, goldfish, white sucker, brown bullhead, redbreast sunfish, and pumpkinseed was assumed to vary directly with standing crop. Species composition was determined as percent of total catch.
Length-weight relationships of important species were established by linear regression of log weight on log length. Analysis of seasonal length-weight relationships provided a measure of growth in weight and an indication of population fitness.
- g. Age and Growth Age and growth samples were collected from four sites:
one upriver, S79400 (Firestone); one near the proposed intake, S77240 (Limerick A); one downriver, S76440 (Limerick B); and one in Vincent Pool, S74365 (Figure 6.1-11). Sites corresponded with large fish population estimate sites described in Table 6.1-12.
6.1-21
LGS EROL Age and growth specimens were collected by dc electrofishing with an aluminum boat equipped with a bow shocking cage (6.1.1.2.1.6e). Collections were made in conjunction with population estimate sampling in odd-numbered years.
Pectoral spines were used to age brown bullhead. Scales were used to age all other fish species. Both pectoral spines were removed from sample specimens. Scale samples were taken from one of two areas on the left side of the fish. Soft-rayed fishes were sampled above the lateral line just below the point of origin of the dorsal fin, and spiny-rayed fishes were sampled below the lateral line at the tip of the extended pectoral fin. Scale (spine) samples from each fish were placed in separate scale envelopes on which species, FL to the nearest millimeter, weight to the nearest gram, sex (determined by gonad inspection or stripping of sex products), collection date, and capture location were recorded.
In the laboratory, scales from all individuals longer than 60 mm FL were soaked in water for 1 to 5 minutes and cleaned of mucous and algae. Scales from smaller fish were usually not soaked. Five to eight uniformly shaped, nonregenerated scales were placed external side down on a 1-mm thick, preheated, cellulose acetate slide, and impressions made with a roller press.
Scale impressions were analyzed using a scale projector at a magnification of 20X. Annuli were identified using criteria given in Tesch (Ref 6.1-26). Length-frequency distributions were used to confirm ages when frequency modes showed acceptable separation. Ages were assigned according to the number of annuli present and the date of collection. From January 1 until annulus formation, age was determined to be one greater than the number of annuli present. After annulus formation age was determined by the number of annuli.
Independent age determinations were made twice, usually by two investigators, and recorded on a preliminary scale reading sheet. Sources of disagreement were analyzed, and concurrence on age and placement of annuli was sought. Scale samples were discarded if concurrence was not attained. Anterior scale radius and distances between annuli and focus were measured from one scale for each fish. Measurements were made to back-calculate the lengths at annuli. To obtain scale radii for use in body-scale regression, five or less unregenerated scale impressions for. a particular fish were measured and a mean was calculated. This method decreased the 6.1-22
LGS EROL likelihood of using a measurement from a single scale of abnormal size.
For spine analysis, the left pectoral spine of each specimen was decalcified by immersion in 0.75 normal hydrochloric acid for about 16 hours1.851852e-4 days <br />0.00444 hours <br />2.645503e-5 weeks <br />6.088e-6 months <br />, and sectioned with a razor blade, a method similar to that described by Wahtola and Owen (Ref 6.1-27). At least three sections were cut from the spine near the distal end of the basal groove. Sections were immediately placed on a glass slide, covered with isopropanol, and read under a dissecting microscope at a magnification of 40X. Annuli were identified using criteria described by Marzolf (Ref 6.1-28). Ages were assigned as described for scales. Annular measurements were made with an ocular micrometer. Spine radius measurements were made on intact pectoral spines using a dial caliper.
To verify age determinations, at least two sections from the same spine were read. In cases of disagreement the spine was discarded. Annular and spine radius measurements were made on the section which exhibited the most distinct annuli.
A least-squares linear regression of body length (dependent variable) on scale (spine) radius (independent variable) produces the best description of the body-scale (spine) relationship. Fork length at each annulus was back-calculated for each fish, based on the body-scale (spine) relationship, using the formula:
L' = C + S' (L-C) (6.1-16) where: L' = length of fish when annulus 'n' was formed L = length of fish when scale (spine) sample was obtained S' = scale (spine) radius of annulus 'n' S = total scale (spine) radius C =.the intercept of body-scale (spine) regression with the abcissa or Fraser's correction factor (Tesch, Ref 6.1-26)
Length at annulus and population age structure were estimated for white sucker, brown bullhead, redbreast sunfish, and pumpkinseed. Population age structure was used to forecast trends in abundance of important species.
6.1-23
LGS EROL
- h. Vincent Pool Trap Net Fishes collected in this program included members of the families Amiidae, Anguillidae, Esocidae, Cyprinidae, Catostomidae, Ictaluridae, Centrarchidae, and Percidae.
Species collected were either sought by fishermen (Ref 6.1-29) or provided forage for sport and pan fishes.
Vincent Dam is located 5.8 km downriver of LGS. Vincent Pool is approximately 3 km long, 190 m wide, up to 4 m deep, and is primarily deep run habitat bordered by overhanging trees along each shoreline. Substrate was boulders, gravel, and silt. A few fallen trees provided cover. Aquatic vegetation was generally sparse.
However near the Montgomery County shore midway from the head of the pool to the dam, a dense stand of Jussiasea was present most of the year. Also, from late summer through fall dense stands of Spirogyra, Cladophora, Myriophyllum, and Potamogeton were present in the upstream reaches of the pool.
In May 1971, six net stations were established (S73810-5, S73800-1, S72960-1, S72950-5, S72100-1, S72120-5) (Table 6.1-13). The "-1" and "-5" of the station designators represent the Chester and Montgomery County shores, respectively. The pool, from the Citizens Utility Company water treatment plant to Vincent Dam, was divided into three sections of equal length. Two nets were placed in each section, opposite one another, on each shore. Sampling at net station S72100-1 was terminated in December 1971, due to sampling difficulty caused by numerous submerged obstructions. In May 1973, two new net stations (S74350-1 and S74360-5) were established in the upstream portion of the pool and were sampled until program termination.
Trap nets consisted of two rectangular (0.9 by 1.8-m) metal frames followed by a series of four, 0.8-m diameter, metal hoops, all enclosed in 1.3-cm mesh netting. A 0.9 by 15.2-m leader extended from the body.
Nets were set perpendicular to shore, with the leader extending from shore to the body of the net. Nets of this design most effectively sample fishes exceeding 80 mm FL. However, no size cutoff of individuals <80 mm was applied to collection data because it was assumed that size selective bias was consistent among collections.
6.1-24
LGS EROL Sampling was conducted monthly from 1971 through 1974.
Four samples per month were collected at each station May-October, and two per month December-April. In 1975, two samples were collected per month at each station January-December. In 1976, four samples per month were collected at each station, May-December. Trap nets were fished for two consecutive 24-hour periods. Captured fish were identified to species (see Section 6.1.1.2.1.6c), measured to within a 5-mm FL interval, and released unless needed for additional study.
Physiochemical data (air and water temperature, pH, dissolved oxygen concentration) were recorded at each site when the nets were set, and again when they were pulled. Percent of total catch was calculated for each species collected, to describe species relative abundance. The quantitative abundance of fishes as a group (total catch), of pumpkinseed, and of brown bullhead were described using catch per effort indices.
A unit of effort for trap nets was a 24-hour net day.
6.1.1.2.2 Perkiomen Creek The Perkiomen Creek watershed, biota, and hydrology are discussed in detail in Sections 2.1, 2.2, and 2.4, respectively. Operation of LGS is expected, generally in spring through fall, to require diversion of Delaware River water through approximately 3.9 km of Perkiomen Creek, between the East Branch Perkiomen Creek confluence and the intake at Graterford, Pennsylvania.
The Perkiomen Creek study area (Figure 6.1-13) extended from about 4 km above to 5 km below the East Branch confluence. The reach above the confluence will be unaffected by diversion, the reach between the confluence and the intake will be affected by diversion, and the reach below the intake will be affected by water withdrawal.
The stream gradient in the study area was 2.2 m/km. The habitat was primarily long run, with occasional riffles. Several dams were present. The mean daily discharge of Perkiomen Creek was 10.4 m3 /s, as measured since 1914 at the U. S. Geological Survey gage at Graterford, Pennsylvania. There has been some regulation by Green Lane Reservoir since 1956. Velocity at times of sampling was commonly between 0.10 and 0.36 m/s. Stream discharge increased rapidly following storms. Water quality in the study area was good, as evidenced by a diverse aquatic biota.
Moderate nutrient enrichment was apparent. Refer to Section 2.2.2.2.1 for a description of pre-existing environmental stresses.
Sample stations on Perkiomen Creek were designated by the letter "P", followed by a number indicating the distance in meters 6.1-25
LGS EROL upstream from the mouth of the creek. Where a sample station included several meters of stream, the site number designated the downstream end of the station.
6.1.1.2.2.1 Phytoplankton Samples were collected at P14390, just upstream of the proposed Graterford intake. The sample station was located at the downstream end of a long run, where water depth ranged from 0.5 to 1.5 m and flow was moderate. Samples were collected on three dates in 1973 with a No. 20 (80 micron) mesh plankton net, and monthly in 1974 with a 0.95-1 sample bottle. Sampling and processing methods were as described in Section 6.1.1.2.1.1.
Relative qualitative abundance was recorded as present, common, or abundant.
6.1.1.2.2.2 Periphyton Samples were collected at one station (P14390) located upstream from the proposed intake, at the downstream end of a long run.
Depth was approximately 0.5 m and flow was moderate. Collection gear and field and laboratory methods are described in Section 6.1.1.2.1.2. Samples were collected weekly from August through December 1973. Biomass standing crop and taxonomic composition were recorded.
6.1.1.2.2.3 Benthic Macroinvertebrates The location and description of sample stations on both Perkiomen Creek and East Branch Perkiomen Creek are given in Table 6.1-14.
Due to changing hydrologic conditions and water quality, benthic communities were dissimilar throughout East Branch Perkiomen Creek. Therefore six sample stations were established at approximately 6-km intervals along its 35-km length, to document gradational spatial change which may result from flow augmentation. Two stations were established on an adjacent section of Perkiomen Creek, one 4.1 km upstream from the confluence of East Branch Perkiomen Creek with Perkiomen Creek, and one 800 m downstream of the proposed intake.
All sampling was done in riffle habitat because it was common in the creeks, and benthic richness and production are typically greatest in this habitat type. Sampling in similar habitat at each station reduced variability due to habitat type.
6.1-26
LGS EROL Benthic samples were taken with net samplers, the most commonly used method for collecting benthic samples directly from riffles.
A Surber sampler (sampling unit 0.093 m2 , mesh 0.50 mm) was used in January 1972, a box sampler (0.093 M 2 , 0.35 mm) of the consultant's design from February 1972 through December 1973, and a portable-invertebrate-box-sampler used thereafter (PIBS, Ellis-Rutter Associates, Douglassville, Pennsylvania; 0.1 M 2 , 0.35 mm)
(Figure 6.1-14). The box sampler and PIBS were considered to be the most efficient net-samplers available because (1) the box configuration allowed maximum manipulation of the substrate to depth (hyporheos) without sampler movement, (2) the four-sided construction prevented loss of organisms due to backwash, and (3) the polyester foam base provided a seal with the substrate, substantially reducing loss of animals from beneath the sampler.
One sample, usually composed of four or five replicates (sampling units), was taken monthly from each station, and all sites were sampled on the same date or on two consecutive days. Substrate was sampled to a depth of roughly 10 cm, where sediments allowed.
In the laboratory, each replicate was hand-sorted and the organisms were preserved in 75% isopropanol. After identification and direct count, animals were oven-dried for 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br /> at 600 C, cooled to room temperature, and weighed to the nearest 0.1 mg. Before weighing, all mollusks were placed in HCl until the shells dissolved.
Identification procedures were similar to those described in Section 6.1.1.2.1.4. Identification within the groups Chironomidae (midges) and Oligochaeta (worms) was possible, but extremely time-consuming, and therefore was performed only on selected samples. Keys used for identification were listed beside their respective taxon on the species list (Table 2.2-43).
Macrobenthos was measured in terms of (1) total taxa per sample or selected groups of samples. The number of taxa (primarily genera in this case) in a sample is a measure of the richness component of benthic diversity. This parameter was recorded by station by year. (2) Standing crop density (numbers and biomass per M2 ) for total and-selected taxa. Numbers of organisms were recorded for each taxon in each replicate of each monthly sample.
Biomass was recorded by taxon in 1973 and 1974, and thereafter as replicate totals, all taxa combined. (3) Relative abundance within station. Relative quantitative abundance is the density of an organism (taxon) expressed as a percent of total (all taxa combined) density in a given sample or selected groups of samples, and is an important measure of community structure.
6.1-27
LGS EROL W 6.1.1.2.2.4 Macroinvertebrate Drift Macroinvertebrate drift refers to the downstream transport of benthic macroinvertebrates in freshwater streams. Two stations were established to sample drift, one on Perkiomen Creek (P14390) and one on East Branch Perkiomen Creek (E2230) (Table 6.1-15).
An attempt was made to duplicate as many physical parameters as possible in the selection of sample stations. Studies were conducted for one 24-hour period per month, in months when flow augmentation may have been required (generally spring through fall). Duplicate macroinvertebrate drift samplers (described in Section 6.1.1.2.1.5) were placed side by side (60-cm separation) for a one-hour period every two hours for 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br />, beginning at 1000 hours0.0116 days <br />0.278 hours <br />0.00165 weeks <br />3.805e-4 months <br />. The top of the sampler projected 0.6 cm above the water surface, permitting capture of organisms drifting on the surface. The cross-sectional area normally submerged was 464 cm2 . Samples were field-preserved with 95% isopropanol.
Laboratory and taxonomy procedures employed by this program were the same as for benthic quantitative samples (Section 6.1.1.2.2.3). Biomass was not recorded for individual taxa, but as hourly totals, all taxa combined. In 1973 all components of drift (terrestrial, emergent, and aquatic) were
- enumerated to estimate their relative importance in terms of percent of total drift. Only the aquatic component was analyzed in 1974.
Parameters studied were (1) number of organisms per unit volume of water for total and selected taxa, (2) total biomass of organisms per unit volume of water, (3) taxonomic composition, and (4) total taxa drifting per hour.
Estimates of the mean number and weight of drifting invertebrates per unit3 volume of water were calculated for each drift study.
Flow (m /s) through the samplers was calculated as the product of the cross-sectional area sampled and the mean velocity of water entering the sampler.
Data from each 24-hour study consisted of 12 observations for each of two duplicate samplers. Hourly drift rates were calculated as the mean number (weight) of the two nets. To derive a 24-hour grand mean, these 12 values were summed and divided by 12. This value, when multiplied by 24, was an estimate of the total number (weight) of organisms that would have been collected had sampling been continuous for 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br />.
Mean number (weight) per m3 (density) was computed for each hour using the flow data recorded (Gurley current meter Model 625F) once for the 24-hour interval (mean number or weight x 1000/3600 x mean volume). The sum of these values divided by 12 gave the 6.1-28
LGS EROL mean density (number or weight) of drifting invertebrates per m3 over the 24-hour period.
6.1.1.2.2.5 Fish
- a. Larval Fish Drift and Trap This program was designed to describe the distribution, abundance, and seasonal occurrence of fish eggs and larvae, and to estimate quantities of larvae that may be entrained. Nets were located at creek meter P14390, approximately 15 m downstream of the future intake site, and 3 m upstream of a partially washed out dam (Table 6.1-16, Figure 6.1-15). At this location an island divides the stream into two channels. Drift collections were made from 1973 through 1975 with stationary samplers (see Section 6.1.1.2.1.6a). In 1975 a plywood sampler (Figure 6.1-16) 49.4 x 30.4 cm was also used to sample larval fish drift in shallow riffle areas. This sampler was fitted with a catch-net fastened to a rectangular brass frame. Two wooden larval fish traps (see Section 6.1.1.2.1.6a) were used to collect larvae inhabiting low velocity areas near shore. Sampling frequency, number of nets used, net configuration, and net location for 1973 through 1975 are given in Tables 6.1-16, and 17), Collection techniques, laboratory processing methods, and taxonomic determinations were the same as those previously described (Section 6.1.1.2.1.6a).
Drifting larvae were characterized by monitoring the density (no./m 3 ) of total drift and important taxa.
Density data were used to indicate quantitative abundance, relative abundance, spatial and temporal distribution, and time and duration of spawning.
Calculations of density for each sample day were like those outlined in Section 6.1.1.2.1.6a. Additional information regarding data used to calculate mean larval densities for specific analyses are presented in Table 6.1-18. Peak spawning periods for selected species were approximated using methods previously described (Section 6.1.1.2.1.6a). Estimates of entrainment and total drift past the intake location were calculated as follows:
- 1. The 24-hour augmented flow for each sample date was apportioned into six zones across the stream by multiplying the 24-hour augmented flow by the 6.1-29
LGS EROL relative 24-hour mean water velocity through each of the six drift nets (24-hour augment flow = USGS flow + mu; mu = mean 7-day intake flow given in the PECo flow simulation of 21 May 1978)
Vi.. .Y FZ.6 (6.1-17) where:
FZ = 24-hour flow through respective zone V = mean 24-hour water velocity through the respective drift net F = 24-hour augmented flow.
- 2. Total drift past the intake location during the 24-hour sample period.
DT = Z 6 (Xz) (Fzf) i=1 (6.1-18) where:
DT = total drift Xz = mean 24-hour larval density in respective zone
- 3. Entrainment loss during the 24-hour sample period was conservatively assumed to be equal to the number of larvae drifting within the influence of the intake. Zone of influence was assumed to be the portion of 24-hour augmented flow necessary to equal entrainment volume. Estimates of total 24-hour larval entrainment were calculated as follows:
Case 1 -
If Fe ! Fz4 Then DE (Xz 4 ) Fe Case 2 -
If Fz 4 <Fe- FZ4 + Fz 3 6.1-30
LGS EROL Then DE=(X4)FZ4 + Xz 3 (Fe-Fz4)
Case 3 -
IfFZ4 + Fz 3 Fe5 Fz4 + Fz 3 + Fz 2 Then DEz (Xz4)Fz 4 +( Xz 3 )Fz 3 + Xz 2(Fe- 4 +Fz 3 )
where:
Fe = 24-hour entrainment volume DE No. of Larvae entrained during the 24-hour sample period.
It was assumed that no change in horizontal distribution will accompany flow augmentation, and percent entrainment was calculated in the same manner as for the Schuylkill intake (Section 6.1.1.2.1.6a).
Trap catches were recorded as catch per sample period (total taxa and important taxa) and were used to describe the larval fish community in shoreline areas adjacent to the proposed intake location. The i.mportance and use of these data are discussed in Section 6.1.1.2.1.6a.
- b. Seine This program focused primarily on minnows and young pan and sport fishes. To minimize variability due to habitat differences, stations were situated in areas of similar habitat (Table 6.1-19). All sites were sampled once per month. Gear, collection techniques, and laboratory processing methods were identical to those previously described (Section 6.1.1.2.1.6c). The minnow and young-of-year pan and sport populations were measured using the following parameters: (1) total catch per unit effort (C/f, number of individuals in all taxa combined), (2) important species C/f(number of comely shiner, spottail shiner, or spotfin shiner), (3) number of species per sample, and (4) relative abundance (percent composition of individual species in the total catch).
6.1-31
LGS EROL
- c. Small Fish Population Estimate This program was designed to study the young of the more abundant age 0 sunfish (rock bass, redbreast sunfish, green sunfish, pumpkinseed, and smallmouth bass).
Small-fish populations were examined using the following parameters: (1) estimated number and biomass by species of age 0 sunfish, and (2) relative abundance.
Estimate sites were located near the proposed Graterford intake. P14585 was sampled only in 1975, and P14830 only in 1976. Sites were 20 m long, 5 m wide, and bounded on one side by the shore. Habitat characteristics of the four sites sampled in 1976 are summarized in Table 6.1-20.
Samples were collected annually at each site.
Electrofishing gear, field procedures, and laboratory techniques were the same as those utilized for the Schuylkill small fish population estimate program, except that fish larger than 50 mm were identified to species, measured to the nearest millimeter (FL), and weighed to the nearest gram before being released outside the collection area. Specimens less than 51 mm were preserved and processed as previously described (Section 6.1.1.2.1.6d).
Multinomial population estimates of age 0 sunfish were made within site, as previously described (Section 6.1.1.2.1.6d). Samples collected in 1975 did not contain enough specimens to calculate estimates and confidence limits by species at each site. Catch data were therefore combined by site, and estimates were made for each species. This approach may have invalidated assumptions of the estimate model, but it was the only practical alternative for obtaining removal method estimates.
- d. Large Fish Population Estimate This program was designed to study juvenile and adult large (>50-mm FL) fishes of the pike, sucker, freshwater catfish and sunfish families, and goldfish, carp, and golden shiner. The large fish community was measured using the following parameters: (1) estimated number of an important species/ha (carp, white sucker, redbreast sunfish, smallmouth bass), (2) estimated biomass of an important species/ha, and (3) relative abundance 6.1-32
LGS EROL (percent composition of individual species in the total catch).
Three estimate sites (P14390, P14160, P14020) were situated near the proposed Graterford intake. An additional site (P20000) was located upstream of the East Branch confluence, in an area that will not be affected by diversion. Sites were located in similar habitat (Table 6.1-21).
One population estimate was made for each site in even-numbered years. The electrofishing gear and collection techniques used for this program were similar to those previously described (Section 6.1.1.2.1.6e). However only fish longer than 50-mm FL were marked and considered in estimate calculations.
Single-census Petersen estimates were calculated at P14020 and P14160 because a sufficient proportion of the population could be recaptured in the second sample (Seber, Ref 6.1-18). Catch statistics from each site were used to calculate population estimates for each important species that was recaptured at an average rate of more than three recaptures per sample. The probability of statistical bias using this criterion is less than 1% for Petersen estimates (Ricker, Ref 6.1-24). However multiple-census Schumacher-Eschmeyer estimates were necessary at P14390 and P20000.
Schnabel estimates were calculated to ascertain the accuracy of the Schumacher-Eschmeyer model.
Schumacher-Eschmeyer population estimates and confidence intervals were calculated as previously outlined (Section 6.1.1.2.1.6e). Schnabel population estimates were calculated by the formulae presented by Schnabel (Ref 6.1-23) and later modified by Chapman (Ref 6.1-30) to reduce bias:
Nt = E(Mt Ct) (6.1-19) t Rt + 1 using the notation presented in Section 6.1.1.2.16e for the Schumacher-Eschmeyer model. Confidence intervals were based on the distribution of recaptures according to criteria presented by Seber (Ref 6.1-18). The 95%
confidence interval for Nt was calculated as the sum of the binomial variances:
6.1-33
LGS EROL
= 2(M) +1.96 '(1 -a)+ 1.96 [4(;Rt) +1.96 '(1 -)10][]
Nt 2 Q; Rt) 2 (6.1-20) where: = £(Mt r Ct) 6 = EMt Ct2/(kX.)
Petersen population estimates were calculated using Chapman's ((Ref 6.1-31), cited by Ricker (Ref 6.1-24))
modified formula to reduce bias:
N = (M+1) (C+I) -1 (6.1-21)
R+1 the notation being similar to that previously given, but without subscripts because this is a single-census estimate.
Confidence intervals are based on the distribution of recaptures, according to criteria presented by Davis (Ref 6.1-32) and Seber (Ref 6.1-18). They are placed around the percentage of recapture (a), inverted, and multiplied by M to obtain confidence intervals for l.
For small samples (C<30), confidence limits are taken directly from a table given by Crow (Ref 6.1-33). When CZ30, the normal approximation is used, and 95%
confidence limits are calculated based on a formula given by Cochran (Ref 6.1-34):
P -1,96 +
2C (6. 1-22) where: f = R/M R/C Biomass was estimated for each important species as previously described (Section 6.1.1.2.1.6e).
Numeric and biomass estimates were inspected for differences. Estimates that did not lie within the 6.1-34
LGS EROL other's confidence interval were considered significantly different at the probability level used to calculate the interval. Changes in relative abundance were determined statistically, rather than by inspection.
- e. Age and Growth The growth and age structure of a few important fishes near the proposed location of the Graterford intake were studied. Collections were made in conjunction with population estimates in even-numbered years at sites described in Table 6.1-22. Site P20000 will be unaffected by diversion or intake operation, whereas sites P14390, P14160, and P14020 may be affected.
Sampling gear, field techniques, and laboratory processing methods were previously discussed (Section 6.1.1.2.1.6g). Length at annulus and age structure (number of individuals in each age group) were estimated for white sucker, redbreast sunfish, and smallmouth bass.
6.1.1.2.3 East Branch Perkiomen Creek Hydrologic conditions, water quality, and biotic communities are not the same. throughout the East Branch, and a gradational spatial response of aquatic biota is anticipated as a result of flow augmentation (diversion). For this reason the entire stream (and an adjoining 9-km section of Perkiomen Creek) was studied (Fig. 6.1-13). It is important to note that the discharge of water into the headwaters of East Branch Perkiomen Creek precluded the collection of ecological data from an area that will be unaffected by diversion. The East Branch watershed, biota, and hydrology are described in Sections 2.1, 2.2, and 2.4 respectively.
Sample stations on East Branch Perkiomen Creek were designated by the letter "E", followed by a number indicating distance in meters upstream from the mouth of the creek. Where a sample station included several meters of stream, the site number designated the downstream end of the station.
6.1.1.2.3.1 Periphyton The location and description of sampling stations are provided in Table 6.1-23. For descriptions of gear, field procedures, laboratory procedures, and taxonomic determinations, refer to 6.1-35
LGS EROL Section 6.1.1.2.1.2. Sampling was conducted from May through October, because flow augmentation will occur during this period.
All stations were sampled on the same day. Biomass (standing crop) and taxonomic composition were the parameters chosen to define the periphyton community. For definitions refer to Section 6.1.1.2.1.2.
6.1.1.2.3.2 Benthic Macroinvertebrates Refer to Section 6.1.1.2.2.3.
6.1.1.2.3.3 Macroinvertebrate Drift Refer to Section 6.1.1.2.2.4.
6.1.1.2.3.4 Fish
- a. Larval Fish Drift This program described the abundance, composition and seasonal occurrence of fish eggs, larvae and juveniles drifting in the downstream reaches of the creek.
The sample site (E2650; Table 6.1-24) was chosen because of its proximity to the confluence with Perkiomen Creek and its similarity in stream topography to the Perkiomen Creek station (Section 6.1.1.2.2.5a). In 1973, two adjacent samplers were set downstream of a long pool-run near the head of a riffle. In order to obtain sufficient flow through the nets, the samplers had to be set in five different locations (Figure 6.1-17). Stream topography changed prior to the 1974 spawning season, and consequently only one sampler was placed at the head of the only remaining riffle in 1974. In 1973 and 1974, drifting fish eggs and larvae were collected with plywood samplers (see Section 6.1.1.2.2.5a). East Branch samples were collected concurrently with those on Perkiomen Creek throughout each spawning season (generally May-August). Studies were conducted for one 24-hour period every other week in 1973; weekly day-night (0945-1315 hours and 2145-0115 hours) and monthly 24-hour collections were made in 1974. For each 24-hour study the net was set for six 4-hour periods. Two 3.5-hour samples were collected during each day-night study. Nets were changed more frequently if they became 6.1-36
LGS EROL clogged with algae or leaf litter. Determination of physiochemical parameters, field and laboratory processing of samples, and identification of specimens were described previously (Section 6.1.1.2.1.6a).
Drift density, relative abundance, and time and duration of spawning were used to characterize the larval population. Mean densities were calculated by dividing the sum of larvae collected in all nets (two in 1973, one in 1974) by the sum of water volume sampled by all nets. The volume of water sampled by each net was determined using average water velocity, submerged cross-sectional area of the sampler, and length of sample period. Because sampling duration varied between 1973 and 1974, data were selected from similar sample times when annual results were compared. Further information regarding data used to calculate mean larval densities for specific analyses is presented in Table 6.1-25. Duration of spawning and peak spawning period for some species was estimated as previously outlined (Section 6.1.1.2.2.5a).
- b. Seine This program focused primarily on minnows and young-of-year pan and sport fishes. Fish distribution and abundance in the East Branch are influenced by stream morphometry, cover, and water velocity which will be altered by diversion. Seine stations E36690, E32170, E29810, E26630, E22980, E12440, E5475, and E1890 were established in areas of similar habitat (Table 6.1-26) within each site so that analysis would not be biased by major habitat differences. Gear, collection techniques, and laboratory processing methods were identical to those previously described (Section 6.1.1.2.1.6c). The minnow and young-of-year pan and sport fish community was measured using the following parameters: (1) total catch per unit effort (C/f), (2) important species (common shiner, spotfin shiner) C/f, (3) number of species per sample, and (4) relative abundance.
- c. Large Fish Population Estimate This program was designed to provide information about important juvenile and adult (>50-mm FL) fishes of the pike, sucker, freshwater catfish, and sunfish families, and goldfish and carp. Because diverse habitats of the East Branch supported different fish populations, five lotic and two lentic sites (Table 6.1-27) were necessary 6.1-37
LGS EROL for an adequate stream-wide description of juvenile and adult populations, and an assessment of diversion effects. Lotic sites were situated approximately equidistant throughout the East Branch, and were representative of habitat in adjacent reaches. The number and location of these sites facilitated documentation of existing stress due to the Sellersville sewage treatment plant. Two of several reservoirs on the stream represented a distinct habitat type.
The large-fish community was measured using the following parameters: (1) estimated number of an important species (redfin pickerel, white sucker, yellow bullhead, redbreast sunfish, green sunfish, pumpkinseed, smallmouth bass)/500 m, (2) estimated biomass of an important species/500 m, and (3) relative abundance (percent composition of individual species in the total estimated number of all species).
Estimates were made once for each site in odd-numbered years. An electrofishing apparatus was used to collect fish. For lotic sites, electric current was supplied by a Georator (500 W, 2.2 A, 230 V dc with full wave rectification) mounted in a 2.4-m aluminum boat on wheels. Current was applied to the water by two hand-held probes and a negative electrode suspended from the transom. The boat electrofisher, previously described (Section 6.1.1.2.1.6e), was used to sample lentic sites.
Sampling was conducted in fall, when water was low and clear, and conductivity was high. Estimate sites were isolated from the rest of the stream by 3.2-mm square mesh block seines. Fish were collected by three crew members; two shocked and netted fish, while the third pulled the boat and controlled the Georator. Shores were fished wading upstream; midchannels were fished moving both upstream and downstream.
Each estimate required two sampling days. On the first day, two additional crew members continuously processed the fish and recorded information. Fish were identified to species, measured to the nearest millimeter FL, and marked with one-half fin clips. On the second day, fish were identified, measured, weighed to the nearest gram, examined for marks, and released into a holding pen to prevent reprocessing. Collection procedures for lentic sites were similar to those used for the Schuylkill large fish population estimate program.
In lotic sites, only fish longer than 50-mm FL were processed, in order to minimize bias resulting from the low capture efficiency of small fish. Capture 6.1-38
LGS EROL efficiency was somewhat lower in lentic sites, so only fish longer than 70-mm FL were considered.
Population estimates were calculated using the adjusted Peterson estimate formula, and biomass estimates were calculated as previously outlined (Section 6.1.1.2.2.5d). Occasionally an accurate length-weight regression for a species could not be established at a particular site because an insufficient number of fish were processed. In these cases the length-weight relationship from the nearest site was used, or if none of the sites had an adequate sample size, data from all sites were combined.
- d. Age and Growth The age and growth program was designed to describe growth and age structure of a few important fishes in East Branch Perkiomen Creek prior to diversion. Fish for this program were collected in conjunction with lotic population estimates, in odd-numbered years, at sites described in Table 6.1-28. Lentic sites were not sampled. Specimens were collected with the stream electrofishing apparatus previously described (Section 6.1.1.2.3.4e). Length at annulus, length-weight relationship, and age structure were estimated for white sucker, redbreast sunfish, and green sunfish.
6.1.1.2.4 Glossary Biotic Component: A related group of organisms regarded as part of a biological system or ecosystem; e.g., phytoplankton, macroinvertebrates, and fish are all biotic components of an aquatic ecosystem.
Sample'Site: The physical location where samples were regularly taken; synonomous with sample location and sample station.
Socio-Economic: Related to or involving a combination of social and economic factors such as commercial harvest and sport hunting or fishing.
Young: Fish during their first year of life; synonomous with young-of-year.
6.1-39
LGS EROL TABLE 6.1-1 LIMERICK WATER QUALITY PROGRAM SBMMARYC1)
SAMPLE RIVER RIVER STATION WIDTH DEPTH PERIOD OF DESIGNATMP .T IlRECORD S73880 Home Water Company intake; 3.4 ka 190 3 1975-1977 downstream of LGS discharge S77040 200 m downstream of LGS discharge 100 1 1974-1977 downstream of LGS discharqe S77140 100 m downstream of IGS discharge 100 1 1974-1977 S77660 420 m upstream of LS discharge 100 1 1974-1977 P14390 Graterford coolinq water intake 60 1 19714-1977 P18700 4.3 km upstream of Graterford intake 40 1 1977 E2800 East Branch mouth 18 0.5 1974-1977 E22880 3.3 km downstream of sewaqe 15 0.5 1974-1977 treatment plant 126700 Route 309 bridge in Sellersville 15 0.5 1974-1977 E32300 East Branch headwaters 12 0.3 1974-1977 A11263 Point Pleasant cooling water intake 500 5 1974-1977
()-Sample frequency - Once every two weeks with the exception of station S77660 which was also sampled daily for dissolved oxygen, water temperature, and other selected physical and chemical parameters.
LGS EROL TABLE 6.1-2 (Page 1 of 2)
LIMERICK WATER QUALITY PROGRAM PARAMETERS, PROCEDURES, AND REFERENCES PARAMETER PROCEDURE REFERENCE Water temperature Mercury thermometer 1,2 Dissolved oxygen Iodometric titration 1,2 pH Glass electrode 1,2 Discharge Stream cross-sectional geometry 3 Specific conductance Wheatstone bridge-type cell 1 Total non-filterable residue Gravimetric 1 Total dissolved residue Gravimetric 1 Turbidity Photonephlometry 1,2 Chloride Mercuric thiocyanate 1,2 Fluoride Specific electrode 2 Sulfate Barium chloride 1 Total alkalinity Methyl orange Carbon dioxide Titrimetric Total hardness EDTA-colorimetric Total organic carbon Oxidative combustion 1 2
Biochemical oxygen demand lodometric titration 1 2
Total phosphate-phosphorus Molybdenum blue 1 2
Ortho phosphate-phosphorus Molybdenum blue 2 Ammonia-nitrogen Specific electrode 2 Nitrite-nitrogen Diazotization 2 Nitrate-nitrogen Cadmium reduction, diazotization 2 Sodium Atomic absorption 2 Potassium Atomic absorption 2 Calcium Atomic absorption 2 Magnesium Atomic absorption 2 Iron Atomic absorption 2 Manganese Atomic absorption 2 Arsenic Atomic absorption 2 Boron Curcumin 2 Zinc Atomic absorption 2 Cadmium Atomic absorption 2 Chromium Atomic absorption 2 Cobalt Atomic absorption 22 Copper Atomic absorption 2 Lead Atomic absorption 2 Mercury Atomic absorption 2 Nickel Atomic absorption Selenium Atomic absorption
LGS EROL TABLE 6.1-2 (Cont'd) (Page 2 of 2)
References
- 1. American Public Health Association, Standard Methods for the Examination of Water and Wastewater, 14th ed. APHA, Washington, D.C (1975).
- 2. United States Environmental Protection Agency, Methods for Chemical Analysis of Water and Wastes, USEPA Washington, D.C (1974).
- 3. Welch, P. S., Limnological Methods, McGraw-Hill Book Co., New York (1948).
LGS EFOL ThBlE 6.1-3 SCHUYLKILL RIVER BENTHIC MACROINVERTEBRATE PROGRAM
SUMMARY
C' 'R)
SAMPLE RIVER CURRMNT STATION WIDTH DEPTH AT VELOCITY SUBSTRATE AND PERIOD OF DESIGN7 10) SITE 1m) lmsL. PARTLE SIZ -RECORD 878620 1020 m upriver 100 0.2-0.9 0.3-0.5 Coarse gravel to 1972-1976 of intake rubble 2.5-15.2 cm in diameter S77120 120 m downriver 100 0.4-1.3 0.1-0.3 Coarse gravel to June 1974-of discharqe rubble 3.0-15.0 ac 1976 in diameter S76760 520 m downriver 100 0.3-1.2 0.1-0.4 Coarse gravel to 1972-1976 of discharqe rubble 2.5-15.2 cm in diameter S75770 1470 m downriver 110 0.2-0.7 0.1-0.4 Coarse gravel to 1972-19711, of discharqe rubble 2.5-15.2 cm 1976 in diameter
(')Sample frequency - Once per month.
(&)Gear - From January-April 1972 stations were sampled with a Surber sampler; from Nay 1972 -
December 1976 all stations were sampled with buried cylinder samplers.
LGS EROL TABLE 6.1-4 SC HYLK ILL. RIVER LARVAL FISH DRIFT AND TRAP PROGRAM
SUMMARY
C 1)
MEAN SAMPLE SITE WATER CURRENT STATION SAMPLE DESIGNATION WIDTH DEPTH VELOCITY RIPARIAN PFRIOD OF DS IGN OR TYPE LOCATION m) (cm) (Im/sl MORPHOMETRY SUBSTRATE VEGETATION RECORD 977 560 Drift Adjacent to intake 105 30-120 0.2-0.6 Run Silt, gravel, Wooded 1974-197F rubble Trap Just downstream of 105 9 0.2 Run Heavy silt, Wooded 1975 intake gravel
(&)Sample frequency - Drift; 1970, semimonthly samples taken at 1000, 1200, 2200, and 2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br />.
1975, semimonthly samples taken over 24-hour interval.
1976, semimonthly samples taken over 24-hour interval.
Trap; 1975, semimonthly samples taken over 24-bourtinterval.
LGS EROL TABLE 6.1-5 SCHUYLKILL RIVER LARVAL FISH DRIFT AND TRAP PROGRAM SAMPLE DESIGN, 1974-1976 SAMPLE NO. OF YEAR TYPE SAMPLING FREQUENCY NETS(I) NET CONFIG URATION NET LOCATION IN RIVER(3) 1974 Drift Semimonthly day- 2 4-6 Two columns of two nets East channel: 14,24,34,44 m night collections( ) each and two middle nets from Montgomery County shore 1975 Drift Semimonthly 21-hour 6 At or just off bottom East channel: 14,24,34 m from collections Montgomery County shore; West channel: 10,26,38 m from Chester County shore 1976 Drift Semimonthly 24-hour 6-12 Six columns of two East channel: 10,23,37 m from 6-12 collections nets each Montgomery County shore; West channel: 10,26,38 m from Chester County shore 1975 Trap Semimonthly 21-hour 2 One trap faced upstream, 0.3 to 1.3 m from Montgomery collections (concur- receiving downstream- County shore, approximately 20 m rent with drift moving fish; one faced downstream of drift nets studies) downstream, receiving upstream-moving fish
(')In 1974 and 1976 the upper nets of the column samplers were not used when the water level was less than the depth of one sampler (46 cm).
C2)Day-night samples were taken at 1000, 1200, 2200, and 2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br />.
C3)Figure 6.1-8
LGS EROL TABLE 6.1-6 DATA UTILIZED TO CALCULATE MEAN DENSITIES FOR SPECIFIC ANALYSES OF SCHUYLKILL RIVER LARVAL FISH DRIFT ANALYSIS CALCULATION YEAR Annual variation in I density for 4-month 1974 Four bottom nets in east channel 1000,1200,2200,2400 relative abundance period hours combined (May-August) by taxa 1975-6 Three bottom nets in east channel 1000,1200,2200,2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br /> combined Diurnal periodicity i density (all larvae 1973 All top and bottom nets(') 24-hour period (1000-1000 combined) by hour by hours) sample date 1974 Two top nets (invertebrate nets) 24-hour period (1000-1000 hours) 1975 All bottom nets 24-hour period (1000-1000 hours)
Variation in density X daily density (all 1974 Four bottom nets in east channel 1000,1200,2200,2400 within spawning season larvae combined) hours combined 1975-6 Three bottom nets in east channel 24-hour period (1000-1000 hours)
Horizontal distribution 3 daily density by net for 1974 Four bottom nets in east channel Day (1000 and 1200 hours0.0139 days <br />0.333 hours <br />0.00198 weeks <br />4.566e-4 months <br />) selected time intervals Night (2200 and 2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br />) 1975-6 six bottom nets across stream(g) Day (1000-2000 and 0500-1000 hours) Niqht (2000-0500 hours) 24-hour period (1000-1000 hours)
Comparison of density in X daily density 1975-6 Nets 1-3 combined (west channel) 24-hour period (1000-east channel with density 1000 hours0.0116 days <br />0.278 hours <br />0.00165 weeks <br />3.805e-4 months <br />) in west channel Nets 4-6 combined (east channel)(z)
Diurnal periodicity by X density by hour by date 1975 Six bottom nets across stream 24-hour period (1000-1000 taxa taxa hours)
Variation in density for I daily density by taxa 1974 Four bottom nets in east channel 1000,1200,2200,2400 selected taxa within hours combined spawning season 1975-6 Six bottom nets across stream(2) 24-hour period (1000-1000 hours)
(')Top nets not included on dates when water level too low for their use.
( 2 )Top nets included in 1970 when water level was sufficient.
LGS EROL TABLE 6.1-7 SCHUYLKILL RIVER LARVAL FISH PUSH NET PROGRAM
SUMMARY
(1 ,,
SAMPLE STATION WATER DEPTH CURRENT AQUATIC PERIOD or DES IGNATOR LOCATION AT SITE (cm) SUBSTFATE VELOCITY VEGETATION RBCORD S78973 1373 m upriver of <30 Rubble Slow Rare 1976-1977 Intake, east shore S78432 832 m upriver of 30-60 Silt-gravel Slow None 1975-1977 intake, east shore 577970 370 m upriver of 30-60 Gr ave 1-rubble slow Common 1976-1977 intake, west shore S77550 50 m downriver of 30-60 Silt slow Abundant 1975-1977 intake, east shore S7718h5- 115 m downriver of 60-90 Gravel slow Common 1975-1977 intake, east shore 877320 280 m downriver of <30 Gravel-rubble slow Abundant 1975-1977 intake, east shore 877230 10 m downriver of <30 Silt Slow Common 1975-1977 discharge, east shore S771 61 79 m downriver of <30 Gravel slow Common 1976-1977 discharge, west shore 876970 270 m downriver of 30-60 Rubble Moderate Common 1976-1977 discharge, east shore S76840 400 m downriver of <30 Gravel Slow Common 1975-1977 discharge, east shore S76 794 446 m downriver of 30-60 Rubble Moderate Common 1976-1977 discharge, mest shore S76632 608 m downriver of <30 Gravel-rubble Slow Rare 1976-1977 discharge, east shcre S75781 1459 m downriver of 30-60 Silt Slow Abundant 1976-1977 discharge, east shore
(')Sample frequency - once per week, mid-April through mid-September.
C')Lenqth for all sites was 10 m.
(Page 1 of 2)
TALE Z.1-TABLE 6. 1- 9 SCHUYLKILL RIVER SEINE PROGRAM SUME~ARY'C1,20,3)
ShNPLE -
STATION AQUATIC RIPARIAN LOCATION MORHONRY SUBSTRATE VEGETA2I1 VEGETATION S81750 4150 m upriver of Run, riffle Rock, rubble, Wooded, grass intake, west shore Si it-clay H-eteranthiera, Potainggeton.
Plodea. Cladoybgus, Font inal.is s78900 1300 m upriver of Run Rubble, rock mxrix11ll. Wooded intake, east shore Heteranthera.
Pot amoget on.
Elod-e C1 opho YgntiniIis 5"78460 860 m upriver of Run Rubble, rock Wooded intake, east shore fleteranthera.
Pot ainoetgn.
877960 360 m upriver of Run, pool s8it-clay, C aorbora. Wooded intake, west shore rubble, rock MHr4rioyvl i- 61 Beteranthera,.
Pot amquet on.
87724S0 At discharqe location, Run, riffle Rubble, silt- Cl ador~hor a Wooded, grass west shore clay, rock Fonti na lie Riffle, Beteranthera.
577220 20 m downriver of Rubble, rock, Potamogetgo, Wooded discharqe, west shore backeddy silt-clay Myr iophyllun, CLeadoyCl adohr 877010 230 m downriver of Backeddy Si lt-clay, Wooded discharge, east shore rock, rubble Heterantbill, Pot amocgeton. ~fi 87 6840 400 m downriver of Ba ckeddo, run Silt-clay, Wooded discharge, east shore rubble, rock CLeadoChao ra r
LAGS EROL .R(Paqe 2 of 2)
TABLE 6.1-8 (Cont4d)
SThý ION AQUATIC RIPARIAN DES IGNATOR SUBSTRATE VEGETATION S76620 e mr downriver of a420 Backeddy, Silt-clay, Hooded discharge, east shore riffle, run, rubble pool S76310 930 m downriver of Backeddy Rubble, rock, Heteran t ;era el wooded discharqe, east shore silt-clay 875730 1510 m downriver of Run, pool Clay-silt. Brush discharge. west shore rubble, rock Heteranthera -
Flodep. Clajgubor (I) Sample frequency - once per month.
(E)Length for all sites was 30 m.
CflPeriod of record for all sites - 1975-1977.
LGS EROL TABLE 6. 1-9 Page 1 of 2 SCHUYLKILL RIVER SMALL FISH POPULATION ESTIMATE PRCGRAM
SUMMARY
CI)
SAMPLE CURRENIC 2) PERICC STATION YEARS LENGTH WIDTH MEAN WATER VTEOCITY RIVTARIPN OF DE5S9N R DEPTH (cm) (rn/s SUBSTRATE VEGETATION RECORD S765140-1( 3) 1973(4) 30.4 7.6 Bedrock 1973 S766410-5(5) 1973(0) 30.4 7.6 sand-rubble 1973 1975 40.0 6.0 30 Sandy-gravel Wooded 1975 1976 40.0 6.0 21 0.15 Sandy-qravel Wooded 1976 S769140-5cs) 1973(4 ) 30.4 7.6 Rubble-silt 1973 8770Ofl-1 (3) 1973(4) 30.4 7.6 sand, rubble, Wooded 1973 silt 1974 40.0 6.0 37 0.09 Sandy-qravel Wooded 1974 1975 40.0 6.0 43 Sandy-qravel Wooded 1975 1976 40.0 6.0 37 0.06 Sandy-gravel Wooded 1976 S771410-5(5) 1973(4) 30.4 7.6 Sandy-gravel Wooded 1973 1974 30.0 6.0 56 0.16 Sandy-qravel Wooded 1974 1975 40.0 6.0 63 Sandy-qravel Wooded 1975 1973 30.4 7.6 Sandy-gravel, Brush 1973 rubble 1975 40.0 6.0 55 Sandy-gravel Wooded 1975 s7761*O-1c3) 1974 415.0 6.0 40 0.17 Sandy-gravel- Wooded 1974 rubble 1974 40.0 6.0 42 Sandy-gravel, Wooded 1975 silt 1976 4O0.0 6.0 34 0.15 Sandy-gravel Wooded 1976 silt s7740lIO-1C 1973(4) 30.4 7.6 Sand, rubble, Brush 1973 silt s7774$0-5C5) 1973(4) 30.14 7.6 Rubble-silt 1973 1974 40.0 6.0 49 0.11 silt Wooded 1974 1975 40.0 6.0 58 Silt Wooded 1975 1976 140.0 6.0 149 0.01O Silt Wooded 1976 S779410-1(3) 1973(0) 30.14 7.6 Rubble-silt 1973 5778 40-1(3) 1975 40.0 6.0 34 Sandy-qravel Wooded 1975 S78140-5CS) 1973(4) 30.4 7.6 Rubble-bedrock 1973
LGS EPOL TABLE 6.1-9 (Cont'd) Page 2 of 2 C&)Saample frequency - Once Per year.
(E)Flows not measured in 1973 and 1975.
(3)Chester County shore.
(b)Habitat descriptions for 1973 incomplete, substrate evaluations approximate.
('s)1ontqomery County shore.
LGS EFOL TABLE 6.1-10 SCHUYLKILL RIVER LARGE FISH POPULATION ESTIMATE PROGRAM SMARY(t )
SAMPLE MEAN STATION SITE RIVER RIVER CURRENT PERIOD DES IGNATOR LENGTH WlIDTH DEPTH VELOCITY AQUATIC OF
...M)- -) (M/81 MORPHOMETR YAH2EII-hZi S79400 1800 m upriver of 675 90 0.2-1.5 0.57 Mixed gravel, Deep run and Cladophora, 1974 and Firestone intake rubble, boulder, riffle My12Dbyhl 1977 and bedrock s772140 Contiguous to 800 105 0.2-2.0 0.35 Silt-detritus, Run 1973, 1975, Limerick A intake sand-gravel, and 1977 rubble S76440 Contiguous to 800 110 0.2-2.0 0.31 Silt-detritus Run 1973, 1975, Limerick B discharge sand-gravel, and 1977 rubble 874365 2875 m downriver 400 190 0.2-2.5 0.26 Silt, detritus, Deep run, Clteanthera 1974 and Vincent of discharge sand, coarse shallow bar 1977 Pool gravel
( PSample frequency - once every two years.
LGS EPOL TABLE 6.1-11 SCHUYLKILL RIVER LARGE FISH CATCH PER UNIT EFFORT PROGRAM
SUMMARY
C()
SAMPLE MEAN STATION SITE RIVER RIVER CURRENT PERIOr DESIGNATOR LENGTH WIDTH DEPTH VELOCITY AQUAT IC CF LOCATIOLN __1Eim (m/s) SUESTRATE MORPHOMET:Y PECCIC S79310 1710 m upriver. of 300 90 0.2-1.5 0.58 Gravel, rubble- Deep run, Cladophora, June 1976-Firestone intake boulder, bedrock riffle 1978 IMyriorbllum, S776(90 40 msupriver of 400 100 0.2-2.0 0.38 Sand-qravel, Run June 1976-Limerick A intake rubble, silt- Heteranther, 1978 detritus Pot am~octon-576940 Contiguous to 300 110 0.2-1.5 - Sand-gravel, Run Mvriovhvllum, 1977-1978 Limerick B discharge rubble, silt- Heteranthera detritus Potanioaeto0n S76440 800 msdawnriver 400 100 0.2-2.0 0.30 Sand-qravel, Run Mvriovbvl lum, June 1976-Limerick C of discharge rubble, silt- Beterantberp, 1978 detrit us Potamogeton S74365 2875 m, dcvnriver 400 180 0.2-2.5 0.23 Silt-detritus, Deep run, Mvrioopbvllum, June 1976-Vincent A of discharge sand, gravel shallow bar Hete ran tbera 1978 S72885 43355 m downriver 300 95 0.2-4.0 0.16 Silt-detritus, Deep pool Myriopvbllum June 1976-Vincent B of discharge sand, gravel 197e
( ')sample frequency - Once per month.
LGS EROE TABLE 6.1-12 SCHUIYLKILL RIVER AGE AND GROWrH PROGRAM SUMIaRYCli)
SAMPLE MEAN STATION SITE RIVER RIVER CURRENT PERIOD DESIGNATOR LENGTH WIDTH DEPTH VELOCITY AQUATIC OF LOCATIO (9l 21m W/ei . RECORD S79400 1.8 km upriver of 675 90 0.2-1.5 0.57 Mixed gravel, Deep run and 1976,1977 Fir *ntone intake rubble, boulder, riffle and bedrock contiguious to Boo 105 0.2-2.0 0.35 silt-detritus, Run 1973, 1975, LI--"-':..k A intake sand-gravel, ftrizogpbyll 1976, 1977 rubble Hyxinybysza
-67640 Contic~kOUS to 800 110 0.2-2.0 0.31 Silt-detritus, Run 1973,.197!,
Limer_ýck B discbarqe sand-gravel, Potam~to 1976, 1977 rubble 974 365 2.9 km dovnriver 400 190 0.2-2.5 0.26 Silt, detritus, Deep run, 1976, 1977 Vincent of discbarqe sand, coarse shallow bar Pool gravel CI) Sample frequency - once every two years.
LGS EROL TABLE 6.1-13 SCHUYLKILL RIVER VINCENT POOL TRAP NET PROGRAM
SUMMARY
C )
SAMPLE RIVER RIVER STATION WIDTH DEPTH PERIOD OF DESIGNATOR .Im SGeSTATd MORPHOMETRY 1-1EORD 200 S74360-5(2) 1.5 Gravel, sand Pool, run 1973-1976 200 S7q350-1(3) 1.5 Gravel, sand Pool, run 1973-1976 190 S73810-1(3) 2.5 sand, silt, mud Pool, run 1971-1976 190 S73800-5(2) 2.0 sand, silt, mud Pool, run 1971-1976 120 S72960-1(3) 3.5 Rock, silt, mud Pool, run 1971-1976 120 1971-1976 S72950-5(2) 2.5 Rock, silt, mud Pool, run 150 S72100-1C3,0) 2.0 Rock, silt, mud Pool, run 1971 150 Silt, mud S72120-5C2) 2.5 Pool, run 1971-1976 (I)Sample frequency - May through Oct 1971-1974, four per month; Apr and Nov 1971-1974, two per month; Jan through Dec 1975, two per month; May 2
through Dec 1976, four per month.
( )Montgomery Country shore.
(3)Chester County shore.
(*)Suspended.
LGS EROL TABLE 6.1-14 (Page I of 2)
PERKIOMEN AND EAST BRANCH PERKCIOMEN CREEK BENTHIC MACROINVERTEBRATE PROGRAM S1UMQkRY(',*)
SAMPLE STATION PERIOD DESIGNATOR VIDTH OF AN HAME_ Iml RECDPD( 3 )
East Branch Perkiomen 936725 In the headwaters, 50 m 3 Small to medium rocks over- 1972-1974, Elephant downstream of Elephant lying hard-packed silt-gravel 1976 Rd. bridge and bedrock 232200 Just. uptream of Branch 6 Sand, gravel, and flat rocks 1972-1974, Branch Pd. bridge to 15 cm 1976 526700 just downstream of Main 34 Extensive gramel and sand 1972-1974, Sellersville St. bridge in Sellersville with some rocks to 30 cm; 1976 some silt and macropollution E23000 100 m downstream of 9 Small to large rocks with 1972- 19714, Cathill Cathill Rd. bridge some silt, sand, and gravel - 1976 E12500 30 m downstream of Moyer 20 Mixed rubble 1972-1974, Moyer Rd. bridge 1976 E5600 Just upstream from Wawa 21 Small to large flat rocks 1972-19711, Wa1a Camp Pd. bridge and gravel overlying bedrock 1976 (exposed in some areas)
Perkiaien P22000 Just upstream of Spring 56 Mixed rubble 1972-1971, Spring Mount Mount Rd. bridge, 4.1 km 1976 upstream from the confluence of the East Branch with Perkiomen Creek. The only station that will not be affected by diversion.
LGS EROL (Page 2 of 2)
TABLE 6.1-14$ (Cont'd)
P13600 Just cbwnstream of Route 32 Gravel and sand overlain 1972-1974, Rahns 113 bridqe, 4.3 ka down- by some small to large rocks 1976 stream of the confluence and 0.8 kn downstream of the graterford intake
(')Sample frequency - Once per month.
Cx)All stations were located in riffle habitat where flow was relatively fast and depth at time of sampling ranqe from near 0 (intermittent) to 30 cm.
( 3 )No sampling was conducted in January-March 1974 and January 1976.
LGS EROL TABLE 6.1-15 PERKIOMEN AND EAST BRANCH PERKIOMEN CREEK MACROINVERTERRATE DRIFT PROGRAM sUMNARY")
SAMPLE STATION CURRENT DESIGNATOR WIDTH DEPTEC ) VELOCITY" )
AMNAME L-M ATIZ (10 ACmi JELEL EINBAZZ PEPIOD Of BEOP East Brangh Perk+/-rn=
E2230 Downstream end of a pool- 15 46-61 0.03-0.12 Mixed rubble April-October Haldeman run, 3.5 m upsetrea of a 1973 riffle. 2.4 km upstream from the Perkiomen Creek April-September confluence. 1974 2rkt-me P14390 Immediate vicinity of the 30 61-91 0.10-0.36 Mixed rubble August 1972 Graterford proposed intake, at the downstream end of a pool-run, April -October 3.5 m upstream of a riffle. 1973 3.5 km downstream from the East Branch confluence. April-September 1974
(') Sample frequency' - one 251-bour p:eriod per month.
(&)At times of sampling.
LGS ERCL TABLE 6.1-16 PERKIOMEN CREEK LARVAL FISH DRIFT AND TRAP PROGRAM
SUMMARY
MEAN SAMPLE SITE WATER CURRENT STATION TYPE OF DESIGNATION WIDTH DEPTH VELOCITY RIPARIAN kIum-TRB sum= LOTION _!() .
IQL".s . ORPHOMITIRY SOUMTT YEGEThT. ulopSC RECCPD P14390 Drift 15 m downstream 64 50 0.2 Read of riffle Gravel and Grass, sbrubs, 1973, 1974, 1975 of intake rubble, sand few trees and bedrock P14390 Trap 15 m downstream 64 10 0.01 Bead of riffle Gravel and Grass, shrubs, 1975 of intake ruttle, sand few trees and bedrock
IGS EROL TYABLE 6.1-17 PERKIOMEN CREEK LARVAL FISH DRIFT AND TRAP PROGRAM SAMPLE DESIGN(2)
No. of Net Location Yea Proara Sampling Freauenc. Nets Net Configuration __Itrte~am 1973 Drift Every other week 24-hourc 2 ) 2-4 Two adjacent columns of West channel: 9 r frov two nets each shore of dam 3
1974 Drift weekly dav-niqht( ) 4-6 Two columns of two nets West channel: 6, 9, 12.
monthly 21-hour each and two middile nets 15 m from shore of dam 1975 Drift Twice a month 21-hour 6 Bottom West channel: 6,9, 12, 15 m from shore of dam; East channel: 9, 1.5 m from east shore 1975 Trap Twice a month 24-hour(') 2 One trap faced upstream 0.7 to 1.5 m from west (concurrent with drift) (downstream fish movement); shore appropriately one trap faced downstream 30 m upstream of dar (upstream fish rovement)
(s)In 1973 and 1974 upper nets were not used durinq periods of low (depth <46 cm).
(12)Drift samplers set on even-hour for one hour throuqhout each 21-hour study.
(3)Day-niqht samples were taken at 1000, 1200, 2200, and 2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br />.
(*)Traps were collected and reset every hour throuqhout each 24-hour study.
LGS EPOL TAB*E 6.1-18 PERKIOMEN CREEK DRIFT AND TRAP DATA UTILIZED TO CALCULATE MEAN DENSITIES FOR SPECIFIC AIALYSES AALY SZ CAILATIOS YEAR NETSA Annual variation in Mean density (May-August) 1973 Two bottom nets in west 24-hourt')
relative abundance by taxa channel 1974 Four bottom nets in west 21-hour(')
.channel 1975 Four bottom nets in west 24-hour(S) channel Variation in density X daily density (all 1973 Two bottom nets in west 24-hour(,)
within spawning larvae combined) channel season 1974 Four bottom nets in west 20-hour(l) channel 1975 Four bottom nets in west 24-hour(')
channel Variation in density Daily mean density by' 1974 Four bottom nets in west 24-hourC')
within spawning taxa channel season 1975 Six bottom nets across 24-hour(t) stream Horizontal variation Daily mean density by 1975 Six bottom nets across 24-hour(g) in drift density taxa and net stream Comparison of drift Daily mean channel density 1975 Nets 1-4 combined (west 21-hour(t) density between east by taxa channel; Nets 5-6 com-and west channel bined (east channel)
Diurnal periodicity X daily density by hour 1975 Six bottom nets across 24-hour(t) by taxa by date by taxa stream Temporal variation in Monthly mean density for 1973 Two bottom nets in west 24-hour(')
peak density for carp carp and Levomi8 spp. channel and Lepomis spp.
1974 Four bottom nets in west 24-hourct) channel (1)24-hours = 1000, 1200, 2200, 2400 hours0.0278 days <br />0.667 hours <br />0.00397 weeks <br />9.132e-4 months <br /> combined.
(2)24-hours = Sample every other hour beqinning at 1000 for 24-hour period.
LGS EROI TABLE 6.1-19 PERKIOMEN CREEK SEINE PROGRAM STJM19RYC 1,21 SAMPLE MEAN PERIOD STATION DEPTH RIPARIAN OF L 'MAQO NOPHCmETmy VEGETAION P19775 5.41 km upstream 0.8 Rock, rubble Riffle Wooded, over- 1975-1977 of intake Gravel Run banging brush Sand, silt, Pool and detritus 1975-1977 P16500 2.1 km upstream 0.8 Rock, rubble Riffle wooded, over-of intake Gravel Run hanging brush Sand, silt Pool and detritus 1975-1977 P1111155 Just upstream of 1.0 Silt-detritus Pool Wooded, over-intake and sane banging brush Gravel, rubble Run 1975-1977 P14320 0.1 km downstream 1.0 Silt-detritus Pool Wooded, over-of intake and sand hanging brush Gravel, rubble Run 1975-1977 P141130 0. 3 km down stream 0.8 Rock, rubble Riffle Wooded, over-of intake Gravel Run hanging brush Sand, silt, Pool and detritus 1975-1977 PI13580 0.8 km downstream 0.8 Ro ck, rubble Riffle Wooded, over-o f intake Gravel Pun hanging brush Sand, silt, and detritus (t)Sample frequency - once per month.
CE)Lenqtb of all sites was 10 m.
LGS EROL TABLE 6.1-20 PERKIOMEN CREEX SMALL FISH POPULATION ESTIMATE PROGRAM
SUMMARY
CI ,P2,3)
SAMPLE STATION MEAN WATER MEAN CURRENT RIPARIAN DESIGNATOR DEPTH L(cm)- j'EOCITY (m/s) SUBSTRATE COVEC4) VEGETATION P14225 37 0.06 Gravel A Wooded P14120 25 0.11 Gravel, rubble B Wooded P14640 57 0.11 Rubble, silt B Grass, low brush P14830 48 0.10 Gravel, rubble B wooded 1)Sample frequency - Annual.
(2)Period of record - 1976.
(3)Site Dimensions - 20 x 5 m.
( 4 )A = None, B = Slight amount, C = Moderate amount, D = Extensive amount.
LGS EROL TABLE 6.1-21 PERK TOME N CREEK LARGE FISH POPULATION ESTIMATE PROGRAM
SUMMARY
Ct)
SAMPLE MEAN STATION SITE RIVER RIVER CURRENT P*RIOD DESIG*ATOR LENGTH WIDTH DEPTH VELOCITY RIPARIAN CP AND NANE -I- _ha_ 10 ms 4ULORP1OM RECF LOCATIO WETATOIO P20000 5.56 Im upstream 350 50 - Moderate sand, silt, Shallow and wooded, grass 1976 of intake gravel, rubble deep runs,.
deep pool P14390 Adjacent to intake 645 65 0.8 slow Gravel, rubble Deep runs Grass, shrubs, 1974, 1976 sand, bedrock shoal area few trees 1974, 1975, P14160 0.3 km downstream 220 30 0.6 Moderate Gravel, rubtle, Deep run Wooded, grass of intake bedrock 1976 P14020 0.4 )= downstream 250 30 0.6 Past and Gravel, rubble, Shallow and wooded, grass 1974, 197(
of intake moderate clay deep runs
(')Sample frequency - one estimate rer site In even-numbered years.
LGS EROL TABLE 6.1-22 PERKKCOMER CREEK AGE AND GROWTH PROGRAM SUMIMRY(4 8)
SAM PLE SITE STREAM STATION LENGTH WIDTH MEAN WATER CURRENT RIPARIAN STATION SAMPLE __N_ DEPTH 192 VELOCITY syTn wORPHOlT P20000 5.6 km upstream 350 50 0.8 Moderate Sand, silt, Shallow and Wooded, grass of intake gravel, rubble deep runs. deep pool P14390 Adjacent to intake 645 65 0.8 Slow Gravel, rubble, Deep runs, shoal Grass, sbruts, sand, bedrock area few trees P14160 0.2 km downstream 220 30 0.6 Moderate Gravel, rubble, Deep run Wooded, grass of intake bedrock P14020 0.4 km downstream 250 30 0.6 Fast and Grave l, rubble, Shallow and Wooded, grass of intake moderate clay deep rmns
(&)Sample frequency - One collection per site in even-numbered years.
(E)Period of record - 1976.
LGS EROL TABLE 6.1-23 EAST BRANCH PERKIOMEN CREEK PERIPHYTON PROGRAM
SUMMARY
CI)
SAMPLE STATION WIDTH DEPTH PERIOD OF DESIGNATOR LOCATION RECORD 0.5 E32115 85 m downstream of Eranch 3 August 1973-Rd. bridge December 1974 0.5 E22867 133 m downstream of Cathill 10 1974 Rd. bridge 0.5 August-E8350 0.5 km upstream of mouth of 10 Indian Creek December 1973 E2800 2.8 km upstream of confluence 17 0.9 1974 with Perkiomen Creek ci)Sample frequency - Twice per month.
0 LGS EROL TABLE 6.1-24 EAST BRANCH PERKIONEN CREEK LARVAL FISH DRIFT PROGRAM
SUMMARY
(t)
SAMPLE 87REAN CURRENT STATION WIDTH MEAN WATER VELOCITY RIPARIA* PERIOD OF DESIGNAT DEPTH (MI (Met DflTMZZ VWGETrTIOu 12650 2.4 km upstream 25-50 0.46-0.61 0.03-0.12 Alternated Loose gravel, Wooded, shrubs 1973, 1974 of confluence with pools and some rubble, Perkiomen Creek riffles silt
(')Sample frequency - Biweekly 24-honr studies in 1973; weekly day-night studies in 1974; monthly 24-hour studies in 1974.
LGS EROL TA1BLE 6.1-25 EAST BRANCH PERKIONEN CREEK LARVAL FISH DRIFT DATA UTILIZED TO CALCULATE MEAN DENSITIES FOR SPECIFIC ANALYSIS CALCULATION HOUR Annual variation in Mean density for 4-month 1973 Two adjacent nets 1000 and 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br /> combined relative abundance period (Hay-Auqust) by taxa 1974 One net 0945, 1000, 2145, and 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br /> combined Diurnal periodicity Mean density (all larvae 1973 Two adjacent nets 26-hour period (1000-1000 hours) combined) by hour by sample date 1974 One net 14-hour period (1000-1000 hours)
Variation in density Mean daily density 1973 Two adjacent nets 1000 and 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br /> combined within spawninq (all larvae combined) season 1974 One net 0945, 1000, 2145, and 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br /> combined Diurnal periodicity Mean density by hour 1976 One net 24-hour period (1000-1000 bours) by taxa by date by taxa Variation in density Mean daily density by 1973 Two adjacent nets 1000 and 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br /> combined for selected taxa taxa within spawninq 1974 One net 0965, 1000, 2145, and season 2200 hours0.0255 days <br />0.611 hours <br />0.00364 weeks <br />8.371e-4 months <br /> combined
LGS ERfL TABLE 6.A-26 EAST BRANCH PERRIOMEN CREEK SEINE PROGRAM
SUMMARY
(CIP,2)
SAMPLE SITE MEAN STATION WIDTH DEPTH RIPARIAN SUNMAR AND
!8ThhTE .VEG*AIO FALLr1Owt Intermittent E36690 3 0.8 Rock, rubble Riffle Wooded, over-Gravel Run banging brush Sand, silt, Pool and detritus E32170 '4 1.0 Rock rubble Riffle Yone Intermittent Gravel Run Sand, silt, Pool and detritus E298 10 3 0.8 Rock, rubble Riffle Wooded, over- Intermittent Gravel Run hanging brush Sand, silt, Pool and detritus E26630 5 0.5 Rock, rubble Riffle wooded, over- Intermittent Gravel RPn hanging brush Sand, silt, Pool and detritus E22980 0.8 Rock, rubble Riffle Wooded, over- Constant Gravel Run hanging brush Sand, silt, Pool and detritus E12440 5 0.8 Rock, rubble Riffle Wooded, over- Constant Gravel Run hanging brush Sand, silt, Pool and detritus E5475 6 0.5 Rock, rubble Riffle Wooded, over- Constant Gravel Run banging brush Sand, silt, Pool and detritus E1890 5 1.0 Rock, rubble, Riffle Wooded, over- Constant Gravel Run hanging brush Sand, silt, Pool and detritus
(')Sample frequency - once per month.
(R)Site lenqth - 60 m.
c 3 )Period of record - 1975-1977.
0 LGS .ROL TABLE 6.1-27 EAST BRANCH PERKIOMEN CREEK LARGE FISH POPULATION ESTIMATE PROGRAM
SUMMARY
CI )
MEAN MEAN SAMPLE SITE STREAM WATER STATION LENGTH WIDTH DEPTH RIPARIA14 SUMER AND PERIOD CF DESIGNAO _ia_ _i-l SUBIM MORPHO1ME tY VjMETATIO fAM"UM- RECORD wti~
E36020 378 3.8 0.14 Silt, gravel, Riffle, run, Aquatic vegetation, Trees, Intermittent 1973, 1975, rubble, bedrock pool undercut banks, brush brush 1977 E305'40 400 9.4 0.22 Clay, silt, Riffle, run, Aquatic vegetation, Trees Intermittent 1973, 1975, qravel, rubble pool undercut banks, tree (thin) , 1977 roots pasture E22240 360 11.8 0.24 Clay, rubble, Riffle, run Undercut banks, Trees, Corn tant 1973, 1975, boulder, bedrock tree roots, boulders brush 1977 112040 350 20.0 0.22 Gravel, rubble, Riffle, run Aquatic vegetation, Trees, Constant 1973, 1975, boulders boulders, undercut pasture 1977 banks El 550 300 18.9 0.35 Silt, qravel, Riffle, run Aquatic vegetation. Trees@ Comn tent 1973, 1975, rubble, bedrock fractured bedrock brush 1977 tree roots EL 50ic E15500 300 31 1.37 silt, rubble Pool Undercut banks, Trees, Cornstant 1974, 1975, rubble brush 1977 E5650 38 0.8 silt, rubble Pool Aquatic vegetation, Trees, Constant 1974, 1975, 555 1977 undercut banks, pasture, brush brush
(')Sample frequency - One estimate per site in odd-numbered years.
0 LOS ERQ.
TABLE 6.1-28 EAST BRANUC PRKxZONER CREEK AGE A)D GROWTH PROGRAM SUNMARYRC' 3)
MEAN MEAN SA14PLE SITE STRflM WATER STATION LENGTH WIDTH DEPTH 91PAPIAN VLFRBTATI1 SUNI!EI AVD L
_wI_ a 136020 378 3.8 0.14 silt, qravel, Riffle, runt Aquatic vegetation, Trees, brush Intermittent rubble, bedrock pool undercut banks, brush 330540 400 9.4 0.22 Clay. silt, Riffle, run. Aquatic vegetation. Trees (thin) , Intermittent qravel, rubble pool undercut banks, tree pasture roots 322240 360 11.0 0.24 Clay, rubble, Riffle, run Undercut banks, tree Trees, brush Constant Boulder, bedrock tree roots, boulders 312040 350 20.0 0.22 Gravel, rubble. Riffle, run Aquatic veqetation# Trees, Constant boulders boulders, undercut pasture banks 31550 300 18.9 0.35 Silt, qravel, Riffle, run Aquatic veqetation# Trees, brush Constant rubble, bedrock fractured bedrock*
tree roots c')Sample frequency - One collection per site in odd-numbered years.
(*)Period of record - 1975 and 1977.
MONTGOMERY COUNTY
/'t gd~t~%
1' I IMFRICK G ENERA T ING %d)
STAT ION
?81CM 009 S77660 - 0KV SSUB LIMERICK ISLAND CHESTER COUNTY 0 0.5 IKM. /
SCALE INKILOMETERS Si 3880 .
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT SCHUYLKILL RIVER WATER QUALITY SAMPLING SITES FIGURE 6.1-1
DELAWARE OUTFALL GREEN LANE I RESERVOIR EAST BRANCH PERKIOMEN CREEKo t? 101 5 C
w POTTSTOWN C
rn ca SCHUYLKILL CAI RIVER Location of aquatic chemistry sampling sites in the Delaware River, East Branch Perkiomen Creek, and Perkiomen Creek. Asterisks indicate location of a continuous recording thermograph.
CO)
N COUNTY CHESTER COUNTY 16000 S$71 000 S68000 0 05 MIN SCALE lINKI1olaUiER SCHdYLWKILL RIVER 8ASINR PENNSYLVANIA TIJOYAREA LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT SCHUYLKILL RIVER STUDY AREA FIGURE 6.1-3
f %.0041 LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT PERIPHYTON SAMPLER USED IN THE SCHUYLKILL RIVER AND EAST BRANCH PERKIOMEN CREEK FIGURE 6.14
MONTGOMERY COUNTY I
S79030 N
78 KM 77 KM CHESTER COUNTY 76 KM S75400 0 O.5 1KM I I I ll=, I l LIMERICK GENERATING STATION SCALE IN KILOMETERS UNITS 1 AND 2 ENVIRONMENTAL REPORT MACROPHYTE STUDY AREA IN THE SCHUYLKILL RIVER FIGURE 6.1-5
ALUMINUM MESH (ACTUAL SIZE)
CYLINDER SAMPLER BEING LIFTED
>7!
71 N7,
"ý7 CLEAN GRAVEL & RUBBLE C
A C CYLINDER SAMPLER IN SITU (A) OUTER CYLINDER LIMERICK GENERATING STATION UNITS 1 AND 2 (B) INNER CYLINDER ENVIRONMENTAL REPORT (C) PLASTIC COATED NYLON BAG FOR SAMPLE RETRIEVAL BENTHIC MACROINVERTEBRATE CYLINDER SAMPLER FIGURE 6.14 A
900 LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT MACROINVERTEBRATE DRIFT SAMPLER FIGURE 6.1-7
FLOW MONTGOMERY CHESTER COUNTY COUNTY 1 2 3 INTAKE LOCATION 7 4 5 6 RIFFLE AREA LIMERICK GENERATING STATION LARVAL FISH STATIONS 4-7 SAMPLED IN 1974 UNITS 1 AND 2 LARVAL FISH STATIONS 1-6 SAMPLED IN 1975 AND 1976 ENVIRONMENTAL REPORT LARVAL FISH DRIFT AND TRAP (T)
SAMPLING SITES AT S77560 IN THE SCHUYLKILL RIVER.
FIGURE 6.1-8
C LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT LARVAL FISH DRIFT (A) AND TRAP (B) SAMPLERS USED IN THE SCHUYLKILL RIVER.
FIGURE 6.1-9
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT LARVAL FISH PUSH NET SAMPLER FIGURE 6.1-10
& Illll
k
-N--
CHESTER COUNTY
'1KM 0 05 1KM SCALE IN KILOMETERS SCHUYLKILL RIVER BASIN LIMERICK GENERATING STATION PENNSYLVANIA'- UNITS 1 AND 2 ENVIRONMENTAL REPORT STUDY AREA LARGE FISH POPULATION ESTIMATE AND AGE AND GROWTH SITES
N N
MONTGOMERY COUNTY CHESTER COUNTY PKM i1M IN KILOMETERS SCALE LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT ARIA LARGE FISH CATCH PER UNIT EFFORT SAMPLING SITES FIGURE 6.1-12
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT PERKIOMEN CREEK STUDY AREA FIGURE 6.1-13 L
LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT PORTABLE - INVERTEBRATE-BOX SAMPLER FIGURE 0.1-14
FLOW INTAKE LOCATION T I
234 RIFFLE AREA LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT LOCATION 2 SAMPLED IN 1973 LOCATION 1-4 SAMPLED IN 1974 LOCATION 1-6 SAMPLED IN 1975 LARVAL FISH DRIFT AND TRAP (T)
SAMPLING SITES AT P14390 6.1-16
1 LIMERICK GENERATING STATION UNITS 1 AND 2 ENVIRONMENTAL REPORT PLYWOOD SAMPLER USED TO SAMPLE LARVAL FISH DRIFT IN SHALLOW AREAS.
RUN I
6 2
4 5
ISLAND STIPPLING DENOTES RIFFLE AREAS STATIONS #1-5 SAMPLED IN 1973 LIMERICK GENERATING STATION STATION #6 SAMPLED IN 1974. UNITS 1 AND 2 DASHED LINES INDICATE GRAVEL BAR ENVIRONMENTAL REPORT EXPANSION IN1974 LARVAL FISH DRIFT SITES AT E2650 IN EAST BRANCH PERKIOMEN CREEK FIGURE 6.1-17 A