ML20095J389
| ML20095J389 | |
| Person / Time | |
|---|---|
| Site: | Beaver Valley |
| Issue date: | 12/31/1991 |
| From: | DUQUESNE LIGHT CO. |
| To: | |
| Shared Package | |
| ML20095J381 | List: |
| References | |
| NUDOCS 9205010297 | |
| Download: ML20095J389 (260) | |
Text
{{#Wiki_filter:- _ ____ - - _ 1991 ANNUAL ENVIRONMENTAL REPORT NON - RAD IO LOG I C AL DUQUESHE LIGHT COMPANY BEAVER VALLEY POWEF. STATION s UNITS NO. 1 & 2 9205010297 920427 PDR ADOCK 05000334 R PDR
l l I 1991 ANNUAL ENVIRONMENTAL REPOM NGi-RADIOLOGICAL DUQUESNE LIGIT CDNPANY REAVER VALLEY POWER STATICH UNITS NO. 1&2 Prepared by: Robert Louis Shema William R. Cody Gary J. Kenderes Michael F. Davison Michael R. Noel Gregory M. Styborski Aquatic Systems Corporation littsburgh, Pennsylvania and Donald S. Cherry, Ph.D. Virginia Polytechnic Institute and State University Blacksburg, Virginia and J. Wayne McIntire Duquesne Light Company Shippingport, Pennsylvania
TABLE OF CONTENTS Page LIST OF FIGURES............................................. v L I S T OF T A B LES . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . ~ . . . . vil I. I N T RO DU CT I ON . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 1 A. S CO P E AN D OB J E CT I VES OF TH E P ROG RAM . . . . . . . . . . . . . . . . . . . . . 1 B. S I T E D ES C RI PT I ON . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 II. S UKMA RY AN D CON CLUS . J d . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8 III. ANALYSIS OF SIGNIFICANT ENVIRONMEN'rAL CHANGE. . . . . . . . . . . . . . . . 18 IV. MONITORING NON-RADIOLOGICAL EFFLUENTS . . . . . . . . . . . . . . . . . . . . . . . 19 A. MONITORING CHEMICAL EFFLUENTS . . . . . . . . . . . ............... 19 B. H E RB I C I D ES . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .......... 19
- V. AQ UAT I C MON I TO RI N G P ROG RAM . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20 A. I NT RODUCT I ON . . . . . . , . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20 B. BENTHOS................................................. 20 Objectives.......................................... 20 Methods............................................. 20 Habitats............................................ 24 Conmunity Structure and Spatial Distribution. . . . . . . . 34 Comparison of Control and Non-Control Stations.......................................... 34 Comparison of Preoperational and Operational Datt.............................................. 36 Sun.ary and Conclusions............................. 40 C. PHYTOPLANKTON........................................... 40 Objectives.......................................... 40 -
Methods............................................. 41 Seasonal Distribution............................... 41 Comparison of Control and Non-Control Transects......................................... 49 Comparison of Preoperational and Operational Data.............................................. 49 Summary and Conclusions............................. 50 1
g y TABLE OF CONTENTS (Continued) P, a,$[pe, D. Z OOP LAN KT ON . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 50 Objectives.......................................... 50 Methods............................................. 54 Seasonal Distribution............................... 54 Comparison of Control and Non-Control Transects......................................... 62 Comparison of Preoperational and Operational Data.............................................. 62 Summary and Conclusions............................. 64 E. FISH.................................................... 68 Objective........................................... 68-Methods...................................... ...... 68 deSults............................................. 70 Comparison of Control and Non-Control Transects......................................... 79 Comparison of Preoperational and Operational Data........,..................................... 86 Summary and Conclusions............................. 86 F. ICHTHYOPLANKTON......................................... 87 Objective........................................... 87 Methods............................................. 87 Results............................................. 89 Comparison of Preoperational and Operational Data.............................................. 89 Summary and Conclusions.............................. 94 G. FISH IMPINGEMENT.........................................' 94 Objective........................................... 94 Methodb............................................. 94 Results............................................. 96 Comparison of Impinged and River Fish. . . . . . . . . . . . . . . '96 Comparison of Operating and Non-Operating Intake Bay Collections............................. 111' Summary and Conclusions............................. 111 H. P LAN KTON ENT RAIN MENT . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 112
- 1. Ichthyop1ankton..................................... 112 Objectives.......................................... 112 Methods............................................. 112 Results............................................. .113 Seasonal Distribution............................... 113 Spatial Distribution................................ 118 I
Summary and Conclusions............................. 118 l t l (f s L 11
i' l l l TABLE OF CONTENTS (Continued) Page H. PLANKTON ENTRAINMENT (Con t ' d )
- 2. Phytoplankton............................ .......... 118 Objectives.......................................... 118 Methods............................................. 118 Comparison of Entrainment and River Sample.......... 119 Summary and Conclusions,............................ 119
- 3. Zooplankton......................................... 120
; Objectives.......................................... 120 ! Methods............................................. 120 Comparison of Entrainment and River Samples......... 120 Summary and Conclusions............................. 121 I. Cor bi cu la MON ITORIN G P ROGRAM. . . . . . . . . . . . . . . . . . . . . . ..... 121 Introduction.....................,.................. 121
- 1. Monitoring.......................................... 123 Objectiven.......................................... 123 Methods............................................. 123 Results................ .......................... 128 Summary................ .......................... 147
- 2. Larvae Study........................................ 147 Objective........................................... 147 Methods............................................. 148 Results............................................. 148 Summary............................................. 156
- 3. Growth Study........................................ 157 Objectives.......................................... 157 Methods............................................. 157 Results............................................. 158 Summary............................................. 158 J. Z EB RA MUS S EL MON ITORING P ROG RAM . . . . . . . . . . . . . . . . . . . . . . . . . 158 Introduction.................... ................... 158
- 1. Monitoring................. 5........ ............... 160 Objectives.......................................... 160 Methods............................................. 161 Results............................................. 163
, Summary............................................. 163 111
l TABLE OF CONTENTS (Con tinued) Page VI.- . RE F E REN C ES . . . . . . . . .. , , , , , , , , , , , , , , , , , , . . . . . . . . . . . . . . . . . . . . . . 164 s
- APPENDIX a 1991 CORBICULA CONTROL PROGRAM ENVIRONMENTAL FATE AND EFFECTS STUDIES -
SUMMER AND FALL DOSING STUDIES
.Duquesne Light Company Beaver Valley Power Station I
iv
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r-LIST OF FIGURES > FIGURE Page I-1 ~ VIEW OF THE BEAVER VALLEY POWER STATION , BVPS . . . . . . . . . . . . . 3 J-2 LOCATION OF. STUDY AREA, BEAVER VALLEY POWER STATION, SHIPPINGPORT, PENNSYLVANIA....................... 4 _I-3. OHIO RIVER FLOW (cfs) AND TEMPERATURE ( F) RECORDEL BY THE U. S. ARMY CORPS OF ENGINEERS FOR THE NEW CUMBERLAND POOL, 1991, DVPS............................... 6 V-A-1 SAMPLING TRANSECTS IN THE VICINITY OF THE BEAVER
-VALLEY POWER STATIONS................... ................. 21 V-B-1 DENTHOS SAMP LIN G S TATION S , BVPS . . . . . . . . . . . . . . . . . . . . . . . . . . . 23 V-B-2 MEAN PERCENT COMPOSITION OF THE BENTHOS COMMUNITY IN THE OHIO RIVER NEAR BVPS DURING PREOPERATIONAL AND OPERATIONAL YEARS, BVPS................................... 35
'V-C-1 MONTHLY PHYTOPLANKTON DENSITIES IN THE OdIO RIVER DURING PREOPEPATIONAL (1974-1975) AND OPERATIONAL (1976-1991)' Y EA RS , BVP S . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 43 V-C-2 PHYTOPLANKTCH GROUP DENSITIES FOR ENTRAINMENT SAMPLES, 1991, BVPS.......................................- 45
- V-D-1 MONTHLY ZOOPLANKTON DENSITIES IN THE OHIO RIVEA DURING PREOPERATIONAL (1974-1975) AND OPERATIONAL (1976-1991) YEARS, BVPS................................... 56 V-D-2 ZOOPIANKTON GROUP DENSITIES FOR ENTRAINMENT SAMPLES, 1991, BVPS................................................ 61 V-E -FISH SAMPLING STATIONS, BVPS.............................. 69
- V-F-1 ICHTHYOPLANKTON SAMPLING STATIONS, BVPS................... 88 V-G-1 INTAKE ST RUCTURE , BVPS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 95 V-I-1. PHCff0GFJPHS OF Corbicula WITH LARVAL CAGE AND ZEBRA MUSSEL WITH ARTIFICI AL SUBSTRATE, BVPS . . . . . . . . . . . . . . 122
-V-I-2 Corbicula MONITORING PROGRAM SAMPLING STATIONS OF THE LOWER. RESERVOIR OF UNIT l- COOLING TOWER, BVPS.. . . . . 124 V-I-3 Corbicula MONITORING FROGRAM SAMPLING STATIONS, OHIO RIVER SYSTEM, BVPS................................... 126 v
LIST OF FIGURES (Continued) FIGURE Page V-I-4 Corbicula MONITORING PROGRAM SAMPLING STATIONS, OHIO RIVER SYSTEM, IN THE VICINITY OF THE INTAKE STRUCTURE, BVPS.................................. ........ 127 V-I-5 APPROXIMATE POPULATIONS OF Corbicula IN UNITS 1 AND 2 COOLING TOWERS, DERIVED FROM SURVEYS CONDUCTED IN 1986 THROUGH 1991, BVPS................................... 130 V-I-6 Corbicula MONITORING PROGRAM SAMPLING STATIONS, I N TAK E ST RUCT URE , BVPS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 132 2
'V-I-7 SIZE DISTRIBUTION OF Corbicula (Number /1000 m screen)
AVERAGED FOR EACH MONTH FROM WEEKLY IMPINGEMENT SURVEYS, 1991, BVPS................................................ 145 l V-I-8
SUMMARY
OF Corbicula COLLECTED FROM THE INTAKE STRUCTURE TRAVELING SCREENS DURING IMPINGEMENT SURVEYS, L 1981'THROUGH 1991, BVPS................................... 146 I V-I-9 RESULTS OF Corbicula LARVAE STUDY SIZE DISTRIBUTION IN THE INTAKE STRUCTURE, 1991, BVPS....................... 153 V-I-10 RESULTS OF Corbicula LARVAE STUDY SIZE DISTRIBUTION IN THE UNIT 1 COOLING TOWER, 19 91, BVPS . . . . . . . . . . . . . . . . . . . 154 V-I-ll RESULTS OF Corbicula LARVAE STUDY SIZE DISTRIBUTION IN THE UNIT 2 COOLING TOWER, 19 91, BVPS . . . . . . . . . . . . . . . . . . . 155 vi
.)'
LIST OF TABLES TABLE Page I-I OHIO RIVER FLOW . (cfs)- AND TEMPERATURE (UF) RECORDED BY THE U. S. ARMY CORPS OF ENGINEERS FOR THE NEW CUMBERLAND POOL, 1991, BVPS........................... 7 4 V-A AQUATIC MONITORING PROGRAM SAMPLING DATES, 1991, BVPS...................................................... 22 V-B-1 SYSTEMATIC LIST OF MACROINVERTEBRATES COLLECTED IN PREOPERATIONAL AND OPERATIONAL YEARS IN THE CHIO RI V E R N EA R BVP S . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 25 2 V-B-2 MEAN NUMBER OF MACROINVERTEBRATES (Number /m ) AND PERCENT COMPOSITION OF OLIGOCHAETA, CHIRONOMIDAE, MOLLUSCA AND OTHER ORGANISMS, 1991, BVPS.................. 31 V-B-3 . BENTHIC MACROINVERTEBRATE DENSITIES (Number /m ), MEAN OF TRIPLICATE FOR BACK CHANNEL AND DUPLICATE SAMPLES COLLECTED IN THE MAIN CHANNEL OHIO RIVER, MAY 13,11991, BVPS........................................ 32 V-B-4 ' BENTHIC MACROINVERTEBRATE DENSITIES (Number /m ), MEAN OF TRIPLICATE FOR BACK CHANNEL AND DUPLICATE SAMPLES COLLECTED IN THE MAIN CilANNEL OHIO RIVER,. SEPTEMBER 30, 1991, BVPS.................................. 33
.V-B-5 MEAN DIVERSITY VALUES FOR BENTHIC MACROINVERTEBRATr:S
' COLLECTED IN THE OHIO RIVER, 1991, BVPS................... 37 V-B-6 2 BENTHIC MACROINVERTEBRATE DENSITIES (Number /m ) FOR STATION 1. (CONTROL) AND STATION 2B (NON-CONT ROL) DURING PREOPERATIONAL AND OPERATIONAL YEARS, DVPS . . . . . . . . , . . . . . . . 38 V-C-1. MONTHLY._PHYTOPLANKTON GROUP DENSITIES (Number /ml)
AND PERCENT COMPOSITION FROM ENTRAINMENT SAMPLES, 1991, BVPS................................................ 42 V-C-2 PHYTOPLANKTON DIVERSITY INDICES .BY MONTH FOR ENTRAINMENT SAMPLES , 19 91, BVPS . . . . . . . . . . <. . . . . . . . . . . . . . . . . 46 V-C-3 DENSITIES (Number /ml) OF MOST ABUNDANT PHYTOPLANKTON TAXA COLLECTED FROM ENTRAINMENT SAMPLES, JANUARY THROUGH DECEMBER 1991, BVPS............................... 47 V-C-4 PHYTOPLANKTON DIVERSITY _ INDICES (MEAN OF ALL
. SAMPLES 1973 TO 1991) NEW CUMBERLAND POOL OF THE OH I O RI VE R , BVP S . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 51 vii
1 1 I LIST OF TABLES -{ (Con ti nued )
)
a !
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TABLE Page 1 V-D-1 MONTHLY ZOOPLANKT01 GROUP DENSITIES (Number / liter) l AND PERCENT COMPOSITION FROM ENTRAINMENT SAMPLES, ; 1991, BVPS................................................ 55 V-D-2 MEAN ZOOPLANKTON DENSITIES (Number / liter) BY MONTH FROM 19 7 3 TilROUGli 19 91, OHIO RIVER AND BVPS . . . . . . . . . . . . . . . 58 V-D-3 DENSITIES (Number /li ter ) OF MOST ABUNDANT ZOOPLANKTON TAXA COLLECTED FROM ENTRAINMENT SAMPLES, JANUARY TH ROUGH DECEMB E R 19 91, BVPS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 60 V-D-4 ZOOPLANKTON DIVERSITY INDICES BY MONTH FOR ENTRAINMENT SAMPLES, 1991, BVPS....................................... 63 V-D-5 MEAN ZOOPLANKTOi DIVERSITY INDICES BY MONTH FROM 1973 THROUGH 19 91 IN THE OHIO RIVER NEAR BVPS . . . . . . . . . . . . . . . . . . 65 V-E 1 FAMILIES AND SPECIES OF FISH COLLECTED IN'THE NEW CUMBERLAND POOL OF THE 011I0 RIVER, 1970-1991, BVPS........ 71 V-E-2 NUMBER OF FISH COLLECTED AT VARIOUS TRANS$: CTS BY GILL NET (G), ELECTROFISilING (E), AND MINNOW TRAP , (M) IN Tl!E NEW CUMBERLAND POOL OF THE OHIO RIVER, 1991, BVPS................................................ 74 1 V-E-3 NUMBER OF FISH COLLFOTED BY MONTil BY GILL NET (G), ELECTROFISHING (E), AND MINNOW TRAP (M) IN THE NEW CUMBERLAND POOL OF TiiE 01110 RIVER, 1991, BVPS............. 76 V-E-4 NUMBER OF FISH COLLECTED BY GILL NET, ELECTROFISHING AND MINNOW TRAP AT TRANSECTS IN THE NEW CUMBERLAND POOL OF THE OHIO RIVE R, 19 91, BVPS . . . . . . . . . . . . . . . . . . . . . . . . 78 V-E-5 ELECTROFISHING CATQi MEANS (X) AT TRANSECTS IN THE NEW CUMBERLAND POOL OF T!!E Q110 RIVER, 1974-1991, BVPS........ 80 V-E-6 GILL NET CATG1 MEANS (X) AT TRANSECTS IN THE NEW CUMBERLAND POOL OF THE OHIO RIVER, 1974-1991, BVPS........ 84 V-F-1 NUMBER AND DENSITY OF FIgH EGGS, LARVAE, JUVENILES, AND ADULTS (Number /100 m ) COLLECTED WITH A 0. 5 m PLANKTai NET Ili THE OHIO RIVER BACK CHANNEL OF PHILLI3 ISLAND (STATION 2B) 1991, BVPS.................... 90 3 V-F-2 DENSITY OF ICHTHYOPLANKTON (Number /100 m ) COLLECTED i
. IN THE 0110 RIVER BACK CHANNEL OF PHILLIS ISLAND (STATIvN 2B) 1973-1974, 1976-1991, DVPS................... 93 1
vill
q l i LIST OF TABLES (Continued) TABLE- Page V-G-1 FISH COLLECTED DURING THE IMPINGEMENT. SURVEYS, 1976-1991, BVPS........................................... 97 V-G-2___
SUMMARY
OF FISH COLLECTED IN IMPINGEMENT SURVEYS CONDUCTED FOR ONE 24 HOUR PERIOD PER WEEK DURING 1991, BVPS................................................ 99 V-G-3
SUMMARY
OF IMPINGEMENT SURVEYS DATA POR 1991, DVPS . . . . . . . . 100 V-G-4
SUMMARY
OF FISH COLLECTED IN IMPINGEMENT SURVEYS, 1976-1991, BVPS........................................... 102 V-G-5 . NUMBER AND PERCENT OF ANNUAL TOTAL OF FISH -COLLECTED IN IMPINGEMENT SURVEYS AND IN THE NEW CUMBERLAND POOL OF THE OHIO RIVER,-1991, BVPS.............. .............. 104
.V-G-6
SUMMARY
OF. CRAYFISH COLLECTED IN IMPINGEMENT SURVEYS CONDUCTED FOR ONE 24-HOUR PERIOD PER WEEK, 1991, DVPS..... 105 V-G-7.
SUMMARY
OF Corbicula COLLECTED DURING IMPINGEMENT SURVEYS
. FOR ONE-24-HOUR. PERIOD PER WEEK, 1991, BVPS............... 107 V-G-8
SUMMARY
OF MOLLUSKS (OTFER THAN Corbicula) AND DRAGONFLIES
' COLLECTED IN IMPINGEMENT SURVEYS CONDUCTED FOR ONE 24-HOUR PERIOD PER. WEEK, 1991, BVPS.....-.......................... 108 V-H-1= NUMBERANDDENSITYOFFIgHEGGS, LARVAE, JUVENILES, AND ADULTS (Number /100 m ) COLLECTED WITH A 0. 5 m
- PLANKTON NET AT THE ENTRAINMENT RIVER TRANSECT IN THE OHIO RIVER, 1991, BVPS................................ 114
-V-I-l Corbicula' COLLECTED IN UNIT-1 COOLING. TOWER
' AP RI L 18 , 19 91, ~ BVP S . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 129 V-I-2 Corbicula COLLECTED IN THE OHIO RIVER MAY . 13 AN D = 14 , 19 91, BVPS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 133
'V-I-3 . Corbicula COLLECTED IN THE OHIO RIVER IN THE VICINITY OF THE INTAKE STRUCTURE MAY. 13, 1991, BVPS................ 134
. . V-I-4 Corbicula COLLECTED IN THE OHIO RIVER SEPTEMBER 30, 1991, BVPS.................................. 135
'V-I-5 Corbicula COLLECTED IN THE OHIO R!VER IN THE VICINITY OF THE INTAKE STRUCTURE SEPTEMBER 30, 1991, BVPS.......... 136 ix
LIST OF TABLES (Con tinued)
+
. TABLE Page V-I-6 Corbicula DENSITIES (Clarts/m ) SUMMARIZED FROM BENTHIC MACROINVERTEBRATE COLLECTIONS 1973 THROUGH 1991, BVPS........................................ 137 V-1-7' 3 Corbicola DENSITIES (Clams /100m ) PRESENT IN ICHTHYOPLANKTON SAMPLES COLLECTED WITH A 0.5 m PLANKTON NET IN THE OHIO RIVER 1988 THROUGH 1991, DVPS...................................- 139-V-I-8 SIZE DISTRIBUTION OF Corbicula COLLECTED DURING IMPINGEMENT SURVEYS FOR ONE 24-HOUR PERIOD PER WEEK, 1991, BVPS................................................ 141 V-I-9 - SIZE DISTRIBUTION OF Corbicula, (Clams /1000 m2 )
, COLLECTED DURING IMPINGEMENT SURVEYS FOR ONL- 24-HOUR (: PERIOD PER WEEK, 1991, BVPS...........'.................... 143 V-I-10 RESULTS OF THE Corbicula LARVAE STUDY IN THE INTAKE STRUCTURE AND UNITS 1 AND 2 - COOLING TOWERS,
-1991, BVPS................................................ 149 V-I-ll RESULTS OF THE Corbicula LARVAE STUDY SIZE ' DISTRIBUTION
'IN THE INTAKE STRUCTURE AND TRIITS 1 AND 2 COOLING TOWERS, 1991, BVPS................................................ 1 51 V-I-12 ' MAXIMUM Corbicula GROWTH LENGTH ACl!IEVED IN A FIVE-MONTH -
PERIOD SUMMARIZED FROM THE LARVAE STUDY CAGE COLLECTIONS-1988 THROUGH-1991, BVPS................................... 159 1 1 !^ l I x ( e
a DUQUESNE LIGHT COMPANY J 1991 ANNUAL- ENVIRONMENTAL REPORT l I. INTRODUCTION This repor t - presents a summary of the Non-Radiological Environmental
- Program conduct'ed by Duquesne Light Company (DLC) during calendar year 1991, for the Beaver Valley Power Station (DVPS) Units 1 and 2, Operating License Numbers DPR-66 and NPF-73. This is primarIly an optional program, since the Nuclear Reg ul ator y Commission (NRC) on February 26, 1980, granted DLC's request to delete all of the Aquatic , Monitoring Program, with the exception of fish impingement ( Amendmen t No. - 2 5) , from the Environmental Technical Specifications ETS), and in 1983, dropped the fish _ impingement studies from the ETS program of required sampling along with non-radiological water qual!*" ret 31re-ments. However, in the interest of providing a non-disruptive data base DLC is continuing the Aquatic Monitoring Program. This report also o contains - a Corbicula Control Program to satisfy NPDES requirements of the Pennsylvania Department of Environmental Resources (Appendix).
A. SCOPE AND OBJECTIVES OF THE PROGRAM The objectives of the 1991 environmentti program were: (1) to assess the possible anvironmental impact of plant operation (including impingement and entrainment) on the benthos, fish, and ichthyoplankton communities in the Ohio River, (2) to provide a sampling program for establishing a continuing data base, (3) to evaluate the presence of Corbicula at the BVPS and to assess the population of Corbicula in the Ohio River, (4) to - stedy the growth and reproduction of Corbicula in the intake structure and cooling towers of BVPS, (5) - to monitor for the potential infestation of the zebra mussel into the Ohio River near BVPS, (6) _ to evaluate the impact of a chemical additive utilized in the Unit 1 and 2 river water systems on the aquatic ecosystem in the Ohio River. 1
DUQUESNE LIGHT COMPANY 1991 ANNUAL EtNIRONMENTAL hEPORT B. SITE DESCRIPTION BVPS _ is located on - the south bank of the Ohio River in the Borough of Shippingport, Beaver County, Pennsylvania, on a 501 acre tract of land. The- Shippingport Station once shared the site with BVPS before being decommissioned. Figure I-l shows an aerial view of BVPS. The site is approximately 1 mile (1.6 km) f rom Midland, Penn:;ylvania; 5 miles (8 km) from East Liverpool, Ohio; and 25 miles (40 km) from Pittsburgh, Pennsylvania. Figure I-2 shows the site location in relation to the principal population centers. Population density in the immediate vicinity of the site is relatively low. The population within a 5 mile (8 km) radius of the plant is approximately 18,000 and the only area of concentrated population is the Borough of Midland, Pennsylvania, which has a population of approximately 3,300. l The_ site lies along the Ohio River in a valley which has a gradual slope extendirg from the river (elevation 665 f t. (203 m) ab^ve sea level) to an elevation - of 1,160 ft. (354 m) along a ridge south of BVPS. Plant entrance elevation at the station is approximately 735 ft. (224 m) above set level.
=The-station.is situated on the Ohio River at river mile 34,8, at a loca-tion on the New Cumberland Pool that is 3.3 river miles (5.3 km) down-stream from Montgomery Lock and - Dam and 19.4 miles (31.2 km) upstream from New Cumberland Lock and Dam. The Pennsylvania-Ohio-West Virginia border is 5.2 river miles (8.4 km)- downstream from the site. The river flow is regulsted by a series o2 dams and reservoirs on the Beaver, Allegheny, Monongahela, and Ohio Eivers and their tributaries. Flow generally varies from 5,000 to 100,000 cubic feet per second (cfs). The range of flows in 1991 is shown on Figure I-3 as well as Table I-1. The maximum flow occurred in January (290,000 cfs) .
Ohio River water temperatures generally vary from 32 to 84 P (0 to j 29 C). Minimum and maximum temperatures generally occur in January and July /Augu st , respectively. During 1991, minimum temperatures were 2 i
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LOCATION OP' STUDY AREA, BEAVER VALLEY POWER STATION SHIPPINGPORT, PENNSYLVANIA BVPS 4
[ DUQUESNE LIGilT. COMPANY { 1991 ANNUAL ENVIRONMENTAL REPORT observed; in February and--maximum temperatures- in July and August- ll (Figures'I-3 and Table I-1). BVPS Units.1 and- 2 have a thermal rating of 2,660 megawatts (Mw) . Uni ts 1- and 2 have a design electrical . rating of 835 Mw and 836 Mw, respec-tively. The circulating water systems are a closed cycle system- using a cooling tower to minimize heat released to the Ohio River. Commercial operation of BVPS Unit 1 began in 1976 and Unit 2 began in 1987. l l-l' 5
=
.a DUQUESHESLIGHT COMPANY:
' i 1991 - ANNUAL ENV! rot 1 MENTAL- REPORT
< FLOW (cfs X 1000)
P-8 260 -- - - - - ~ ~ - --- - - - - - - 200 - " - - - - - " - - - - - - - - - - - -
-150 - - - - - -- ----
- 100 - - - - - - - - - - - - - - - - - - - - - -
50 --~ - 0 ' ' '
- JAN FES MAR . APR MAY JUN JUL AUG SEP : OCT NOV. DEC
- TEMPERATURE (oF) -
100 80 - NY"3 - l.
-60 N - --
40', - - - - - - - 20 - 4 0- ' JAN1FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC MONTH-MONTHLY MIN- -+- MONTHLY AVE -*- MONTHLY MAX l -- FIGURE I-3 j[ OHIO RIVER' FLOW-(cfs)-AND TEMPERATURE ( F) p RECORDED BY: TiiE U.S. ARMY CORPS OF ENGINEERS
'FOR THE NEW CUMBERLAND POOL, 1991 BVPS-l-
6
TABLE'I-l OHIO RIVER FLOli, (cfs), AND TEMPERATURE . (UF) RECORDED.BY THE
' U.S. ARMY CORPS OF ENGINEERS FOR THE NEW CUMBERLAND POOL,,1991, BVPS-
- Jan Feb Mar Apr May 'Jun Jul Aug Seg- Oct Nov Dec 3
Flow (cfs x 10 _3. Monthly Maximum 290.0 125.0 154.0 84.0. 56.0 ~ 17.0 '20.5 15.5 17.0 10.0 44.0 96.0 3 o-- Monthly Average 96.5 74.0 79.4 47.9 22.6 9.2 9.1 7.8 7.2 7.0 10.2 33.5 ~E@ Monthly Minimum 38.0 43.0 39.0 25.0 8.0 6.0 6.0 5.0 5.5 5.5 .5.5 ES
>m 9.0
- r p .-
mm-Temperature ( F) C u
-73 3 del Monthly Maximum 41 38 47 57 76 85 87 87 85 63 45 Si 28-Monthly Average 37 34 41 52 63 81 85 83 79 69 56 41 y@'
ca R .: Monthly Minimum 34 33 37 46 56 76 83 80 73 64 50 38 gE o 4.
DUQUESNE LIGitT COMPANY 1991 ANNUAL ENV1RONMENTAL REPORT II.
SUMMARY
AND CONCLUSIONS , The 1991 -BVPS Units 1 and 2 Non-Radiological Environmental Monitoring Program included an Aquatic Program (surveillance 'and tield sampling of Ohio River aquatic life) and a C,or bi cul.a Control Program study. The Aquatic Program is an annual program voluntarily conducted by Duquesne Light Company to assess the impact of the operating DVPS on the aquatic ecosystem in the Ohio River, principally the New Cumberland Pool. The Corbicula Control Program was condus ted in 1991 by Duquesne Light Company for the BVPS Units 1 and 2 to assess the et ficacy and impact of a chemical additive on the aquatic ecosystem and complies with NPDES l requirements established by the Pennsylvania Department of Environmental Resources. This is the sixteenth year of operational environmental
.conitoring for Unit 1 and the fourth for Unit 2. As in the previous years, no evidence of adverse environmental impact to the aquatic life in the Ohio River near LVPS was observed.
AQUATIC MONITORING PROGRAM The Aquatic Environmental Monitoring Program included studies oft benthos,, fish, ichthyoplankton, impingement, plankton entrainment, Corbicula and zebra mussel. Sampling was conducted for benthos and fish upstream and downstream of the plant d ur ing 1991 to assess potential impacts of BVPS discharges. These data were also compared to preopera-tional and other operational data to assess long-term trends. Impinge-ment and entrainment data were examined to determine the impact of withdrawing river water for in-plant use. Corbicula studies were con-ducted to determine the presence of these clams in the Ohio River and their growth and reproduction inside the plant. Plant and river sam-pling was performed in 1991 to monitor for the potential infestation of the zebra mussel into the Ohio River near BVPS. The following para-graphs summarize these findings: Benthos. Substrate was probably the most important f actor controlling the distribution and abundance of the benthic macroinvertebrates in the Ohio River near BVPS. Soft muck-type substrates along the shoreline 8
DUQUESNE LIGHT CiMPANY 1991 ANNUAL ENVIRONMENTAL REPORT were conducive to worm and midge proliferation, while limiting macro- ! invertebrates which require a more. stable bottom. At the shoreline
, stations, Oligochaeta accounted for 86% of the macrobenthos collected, whereas Chironomidae and Mollusca each accounted for about 9% and 5t, respectively. Community structure has changed little since preoper-ational years and there were no ind; cations that BVPS operations were affecting the benthic community of the Ohio River, l'
Phytoplankton. The phytoplankton community of the Ohio River near BVPS l exhibited a slightly modified seasonal pattern compared to those
=
observed in previous years. This pattern, although different from other L years for the Ohio River near BVPS, is common to temperate, lotic envi-ronments thac experience frequent warm water and low turbidity condi-tions. Total cell densities were within the range observed during previous years. Although blue-green algae dominated the phytoplankton during the summer, the species' composition remained similar to that of the previous years. Diversity indices were within the range of those
'previously observed near BVPS.
! Zooplankton. Zooplankton densities throughout 1991 were typical of the temperate zooplankton community found in large river habitats. Total
- i. densities exceeded the range of those reported in preoperational and several operational years. Populations developed highest densities in May and a secondary peak occurred in September. Protozoans and rotif ers were always predominant. Common and abundant taxa in 1991 were similar to those reported during preoperational and operational years. Shannon-Weiner diversity, number of species, and evenness were within the ranges
! of-preceding years. Based on the data collected during the 16 operating _ years (1976 through 1991) .and the three preoperational years (1973 through 1975), it is concluded that the overall abundance and species composition of the zooplankton in the Ohio River near BVPS has remained l stable and pos::ibly improved slightly over the nineteen-year period f rom 1973 to 1991. The data indicate that increased turbidity and current l f rom hign water conditions have the strongest effects of delaying the
, populations' peaks and temporarily decreasing total zooplankton densi-I ties in the Ohio River near BVPS.
l I 9
DUQUrWE. LIGilT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT Fish. ' The fish community of the Ohio River in the vicinity of BVPS has been sampled from 1970 to present using several types of gear s electro-fishing, gill netting, and periodically, minnow traps and seines. The ,
. results, of- these fish surveys show normal community str acture based on species composition and relative abundance. In all the surveys since 1970, forage species were collected in the highest numbers. This indi-cates a normal fish community, since game species (pr eda tor s) rely on this forage - base for their survival. Variations in total annual catch are a natural occurrence and are attributable primarily to fluctuations in the population size of the forage species. This was evident in 1991 with the abundant population of gizzard shad present in the Ohio River near BVPS. Forage species, such as gizzard shad, with high reproductive potentials frequently respond to changes in natural environmental factors (compe ti tion, food availability, enver, and water quality) with large changes in populstion size.
l Although variation in total catch has occurr eo, species composition has ! remained fairly stable. Since the initiation of stu.1tet an 1970, forage j fish have dominated the catches. Carp, cho-nael catfish, smallmouth and I spotted bass, and walleye have all remained ca;nmaa species. Since 1978, sauger have become a common game species nea; BVPS. i: l Differences in the' 1991 electroff'tq and gill net catches between the Control and Non-Control Transect, we.e sir :.lar to previous years (both operational and preoperationalL) and -were probably caused by habitat pre-ferences-of-individual species. This habitat preference is probably the most influential f actor that af fects where the dif f erent species of fish
-are collected an. in what relative abundance.
Data collected f ra.1970 through 1991 indicate that fish in the vicinity of'the power plant have not been adversely affected by BVPS operation. Ichthyoplankton. Gizzard shad and freshwater drum dominated the 1991 1;hthyoplankton catch from the back channel of Phillis Island. Peak densities occurred in May and consisted mostly of eggs. April showed little spawning activity. The ichthyoplankton densities for June and 10
DUQUESNE LIGitT COMPANY 1991 ANNUAL EN1/8RONMENTAL REPORT July were lower than most of the previous totals for those months t reported in previous survey years. Fish Impingement. The results of the 1991 impingement surveys indicate that withdrawal of r.iver water at the BVPS intake for cooling purposes has very little effect on the fish populations. Two hundred sixty (260) fishes were collected, which was comparable to other yearly totals since initial operation of DVPS in 1975. Freshwater drum were the most numer-ous fish, comprising 39.2% of the total annual catch. The total weight of all fishes collected from the 1991 fish impingement surveys was 2.2 kg (4.8 lbs.). Of the 260 fir collected, 107 (41.2%) were alive and returned via the discharge pipe to the Ohio River. Plankton Entrainment. Entrainment studies were performed to investigate the impact on the plankton community by withdrawing river water for in-plant use. Entrainment-river transect surveys for ichthyoplankton were conducted to ascertain any changes in spawning activity occurring in the Ohio River adjacent to the BVPS intake. The greatest abundance of ichthyoplankton collected occurred during the month of May. Assuming actual entrainment rates were similar to those found in 1976 through 1979, and adjusting for the water withdrawn for Unit 2, no substantial entrainment losses should have occurred in 1991 due to the operation of BVPS. Assessment of monthly phytoplankton and zooplankton data of past years indicated that under conditions of minimum low river flow,-approx-imately St of the phytoplankton and zooplankton passing the intake would be ' withdrawn by . the BVPS circulating water system. This is considered , to be an extremely cmall loss of phytoplankton and zooplankton relative to the river populations. Corbicula Monitoring, corbicula monitoring, consis ting of river and plant surveys, was conducted to determine.the presence of these clams in the Ohio River and the circulating river water system of the BVPS (in- - take structure and cooling towers). The Corbicula Montoring Program was initiated in 1985, and has been expanded in subsequent years, 11
DUQUESNE LIGitT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT
-Sampling of sediments in the Unit 1 cooling tower reservoir was per-formed on April 18, 1991 during a scheduled outage, in order to estimate the Corbicula population within that structure. The Corbicula popula- ;
tion in the reservoir was estimated to be 160.0 million clams (99.9% dead), based upon the ' seventeen ponar dredge samples collected. All ; clams were removed from the Unit 1 cooling tower basin during this outage. Population surveys of both BVPS cooling tower reservoirs con-
. ducted during scheduled outages (1986 through 1991) have resulted in lower estimates of Corbicula in the Unit 2 tower compted to the Unit 1 1 cooling tower. This can be attributed to dif f erences in cooling tower I
design'and the faster water currents in the Unit 2 cooling tower reser- l voir, which decrease sediment deposition. i
.The river surveys conducted in 1991 demonstrate -that Corbicula inhabit-ing the upper _0hio drainage provides a large number of clams to the BVPS. Corbicula densities in 1991 at srmpling stations above and below the plant remained either steady or were comparable to densities found in the past two years. Cleaning of the intake bays in the spring and fall by divers resulted in removing many live clams from the inner bays; i this along with the weekly impingement data show that juvenile and adult clams move into'the plant with the water currents.
Corbicula, which colonized the larval cages housed in the BVPS intake structure during the summer of 1991, exhibited vigorous growth during the five-month colonization period. Almost half (47.0%) of the live Corbicula removed fran the intake structure larval - cages in August through Novent~r were . cetained on the three largest . mesh size sieves (9.5, 12.5 and 16.0 mm) during the size analysis. Elevated river water temperatures throughout the summer and early f all probably contributed to the rapid growth of these clams, in conjunction with an adequate food source-for these filter feeders., The use of CT-1 molluscicide (1991 DLC Corbicula Control Program) on December 10, 1991 in the Unit 1 river water system produced 31.5% mor-tality (62 dead Corbicula) in the larval cage removed from the Unit 1 cooling tower on December 12 (two days post-dosing). Mo;tality was 12 l
DUQUESNE LIGHT COMPANY 1791 ANNUAL ENVIRONMENTAL REPORT greater (92.9%) in the larval cage removed f rom this BVPS structure on January 24, 1992. The Unit 2 cooling tower larval cages contained low numbers of Corbicula .(not greater than 45 per mc.n th ) during the li91 monthly surveys. The use of CT-1 molluscicide in the Unit 2 river water system on August 21, 1991 produced 100% mortality (three dead Corbicula) in the larval cage removed one month after dosing (September 20) . Recolonization of Unit 2 larval cages exposed to the molluscicide was first noted in the cage. re>.oved on November 15 (20 live Corbicula). The recolonization of molluscicide exposed larval cag: was previously noted during the CT-1 molluscicide dosing of the Unit 1 cooling tower on June 20 and 21, 1990. Both studies tend to indicate that no residual sedim,ent toxicity is evident af ter CT-1 molluscicide application. > Corbicula larvae which colonized the intake structure larval cages exhibited the most rapid growth and reached larger sizes than those entering the cages during the < inter and early spring. Corbicula removed f rom the - Units 1 and 2 larval cages generally have not attained the maximum sites observed for clams removed from the intake structure cages for the same period. This may be due to chlorination in the cooling towers. Zebra Mussel Monitoring. The zebra mussel (Dreissena @orpha) is an exotic freshwater mollusk that is believed to have been introduced into Lake St. Clair in 1987 via ballast water of ocean-going cargo vessels. . Since then they have spread rapidly to the other Great Lakes and are infesting f reshwater systems in the United States. Due to the proximity of the Ohio River to Lake Erie, BVPS initiated a Zebra Mussel Monitoring Program in January 1990. The Zebra Mussel Monitoring Program utilizes artificial substrates which provide a large surf ace area for the mussel larvae to attach. In 1991, as the result of plant and river sampling, no zebra mussels have been detected. 13-
DUQUESNE LIGilT COMPANY 1;91 ANNUAL ENVIRONMENTAL REPORT Corbicula CONTROL pFOGRAM
.termission was granted by the Pennsylvania Department of Environmental Resources (DER) to use a chemical additive (Clam-Trol or CT-1) in com-bination with a ' detoxification agent (DT-1), a bentonite clay, in the Beaver Valley Power Station Unit.1 and 2 river water systems in 1991.
Reasons for the use of the molluscicide CT-1 in the water systems included the proliferation of Asiatic clam (Corbicula) densities within the plant and cooling towers, intrusion into and clogg ing of heat exchangers, and the need to develop an effective biof ouli ng control system to prevent the invasion of the migrating zebra mussel (Dreissena polymorpha) which is near in proximity (Great Lakes). The Nuclear Regulatory Commission (NRC) . advocates the development of an antibiofoul-ing program by the nuclear power industry. t In accordance with ~ permission granted by the DER, two specific research studies were carried out in 1991: a summer dosing study which continued for 40 days af ter CT-1 application, and a fall dosing study of similar duration. To assure ecological integrity of the Ohio River receiving system during the chemical additive process, a diversity of toxicological, ecological, and physiological tests were conducted. Test species included inverte-brates and vertebrates. The invertebrates tested ' included daphnids (Daphnia magna, Ceriodaphnia dubia). that reside in the water column, clams, snails, and midges (Chironomuu riparius) that inhabit the' river sediments. The fathead minnow (Pimephales promelas) and bluegill (Lepomis macrochirus) were the vertebt ate species tested. In short, a multi-species approach was adopted. , A ' three-tiered approach was employed which included formal laboratory toxicity -testing . at Virginia Polytechnic Institute (acute toxicity and 7-day survival-impairment); an on-site experimental stream facility which provided greater environmental realism than formal laboratory testing; and biosurveys (benthic macroinvertebrates) carried out in the 14
DUQUESNE LIO!!T COMPANY j 1991 ANNUAL ENVIRCAMENTAL REPORT l
'l
)
river. These tests have been developed and/or endorsed by the US EPA and ASTM and are state-of-the-art ecotoxicological protocol. Summer Dosing S tudy . On August 21-22, 1991, the plant (Uni t 2) was dosed with CT-1 s DT-1 for 18 hours in an effort to control Cor bicula inf estation within the plant. The formal laboratory toxicity-impairment testing occurred at Virginia Tech while artificial stream evaluations of the effluent occurred in the environmental laboratory at the plant. Benthic macroinvertebrate densi ti es in the river were evaluated to corroborate the laboratory and in-river studies. Ceriodaphnia survived an acute ef fluent Cr-1:Ur-1 exposure of 5 to 40% but had 100% mortality at 100% effluent. Ceriodaphnia suffered no significant mortality or reproductive impairment at 20% ef fluent, while fathead minnow had no deleterious consequences. through 100% effluent. Therefore, no impairment occurred at the IWC which was 5% etfluent. When the same effluent was evaluated 2 weeks later, no negative sur-vival or reproduc tive impairment could be found thre> ugh 100% effitent concentrations. The CT-1 Dr-1 dosing in the plant did inhibit Chironomus growth in the river sediment station downstream but not in the sediments of the bor-atory artificial streams. Chironomid growth in the river sediments below the plant at PS and 2B continued to be impaired through the 40 days following mollusc 1 cide dosing. Subsequent tes ti ng of the river sediments was developed in the fall prior to dosing to determine the-potential for recovery. Corbicula growth was impaired in the artificial streams at 50% effluent but not at 100%. In the river, Corbicula growth was impaired at . S tations PS and 2B 35 days after dosi ng . Bluegill sunfish growth - in the artificial streams was not impaired af ter dosing but survivorship was. Effects upon sn.iil (Goniobasis sp. ) and Corbicula survival were negligible throughout the ar tificial stream studies. .Macroinvertebrate benthological data were similar before, just after and 40 days after in-plant dosing. Organism occurrence and density were patchy and 'a function of the type and amount of sediment available. 15
DUQUESNE LIGHT COMPANY
, 1991 ANNUAL ENVZRONMENTAL REPORT No foam was - generated in the effluent during the. in-plant dosing with CT-1:DT-1 as a-result of- cxidation of slime (algal, fungal, bacterial) g buildup in river water service lines. Clams held in bioboxes in the Cooling _ Tower _-were succen tully_ eradicated -within 5 days following exposure to . CT-1, and in general, both juvenile and adult clams were equally sensitive.
. Fall Dosing Study.- On December 10-11, 1991, the plant (Unit 1) was dosed with CT-1 DT-1 for a period of 16 hours f or Corbicula control after the fall spawning period had ended. As in the spring study, three tiers of testing (formal laboratory, on-site laboratory, macroinvertebrate monitoring in the river) were utilized.
In the . seven-day survival-impairment tests, Ceriodaphnia survival and reproduction were not aff ected at the IWC but had reproductive impa i r-ment at lot effluent -concentration and higher. Fathead minnow survival.
' impairment tests , indicated survivorship occurred through 100% effluent while the NOEC was at-10% effluent.
Prior to plant dosing in the fall, sediment at Stations PS and 2B were, et ,luated for potential impairment of Chironomus growth. No impairment I was. observed in the 9 /29,'92 sample or in subsequent samples taken on ll/5/91.and 11/25/91. The CT-1:DT-1 dosing .in the plant did not inhibit Chironomus and Asiatic clam growth in the river sediment or in laboratory experimental streams. In general, growth was: greatest at the river station closest to the effluent discharge and in the 50 and 100% effluent-treated streams.
- Survivorship was 100% for both sediment-dwelling organisms. Survivor-ship of snails (Goniobasis sp. ) in the- artificial streams was 100% and nearly so. ( ~ 954) for Corbicula. . This trend continued af ter 35 days into
' January 1992 and indicated that potential thermal enrichment in fluenced the ecological integrity of the sediments in the on-site laboratory and
-river receiving system. Patterns of macroinvertebrate benthological i data were similar to those found in the summer study and earlier (spring N
! and fall, 1990). I: 16 1
DU90ESNE LIGitT COMPANY'- 1091 ANNUAL ENVIRONMENTAh REPORT Macroinvertebrate benthological data had no 1.iusual trends among each of u+ samp*ing periods before, just after and 34 dayu after in-plant \_ dosing. Where sediment was limited in the middle of the discharge .~t channel, organism abunda..!e was patchy. Organism occurrence and density were a function _of 'che type and amount of sediment available. I As . ras the case during summer dosing of the plant, foan generation was ' not a problem daring the fall. Clams held in bloboxes in the Cooling Tower were not as successfelly controlled as they were during the t.ummer j dosing. After 25 days of surveillance, 43 and 87% of the adults and j juveniles, respectively, were eradicated. l l I t e T l l l l-l l 17
. . _ . . , . . . - . . . - - - - - - - - .. .~.- - ---- - - - -
DUQUCSNE LICllT COMPANY 1991 ANNUAL ENVIR0flMENTAL REPORT 111. ANALYSIS OF SIGNI7! CANT EIN!RONMENTAL O!ANGE The BVPS Unit 1 ETS, Appendix B to Operating License No. DP R- 6 6, ini-tially required that significant environmental change analyses be per-formed on benthos, phytoplanston, and rooplankton data. However, on February 26, 1980, the NRC granted DLC a reqJest to delete all of the Ag tatic Monitoring Program, with the exception of fish impingement, f rom the ETS (Amendment No. 2$, License No. DPR-6 6) . Consequently, the requirements for Analysis of Significant Environmental Change was deleted by 'the NRC, and is not applicable to the present Aquatic - Monitoring Program. In 1983, the NRC also deleted the requirement for fish impingement studies, flowever, in the intersst of providing a non-disruptive data base, DLC is continuing the Aqua tro Monitoring I'rogram. 9 3 4 1 4 e 1 18 1
DuguEstic LIGitT COMPANY 1991 ANiiUAL D4VIROtiMENTAL REPORT IV. MONITORING NCri-RADIOLOGICAL EFFLUENTS
, A. MONITORIt40 CHEMICAL EFFLUENTS The Environmental Technical Specifications (LTS) that were developed and included as part of the licensing agreement for the BVPS, regulf ed that certain non-radiologlN1 chemicals and the temperature of the discharges be monitored and if limits were exceeded they had to be reported to the N RC . During 1983, the NRC (lutendment No. 64, License No. DPR-66) deleted these water quality requireinents. The basis for this deletion la that the reporting requireme.ers would be administered under the NPDES permit. Ilowever, the NRC requested that if any NPDES permit requirements were exceeded, that a copy of the violation be forwarded to the Direc-tor, Of fice of Nuclear Reactor Regulation.
B. HE RBICIDES Monitoring and reporting of herbicides used for weed control during 1991, is no longer required as stated in Amendment Jio. 64 thus, this information is not included in this report. e 4 l 19 __ _ _ -- . _ . _ _ __ . ~ . ._. . . . _ .
DU90ESNE L1GitT COMPANY 1991 AllNUAt. ENVIRONMcNTAL RCPORT V. AQUATIC MONITORING PROGRAM A. INTRODUCT! ON -- The' environment 31 M 4? area established to assess potential impacts consisted of thr< vulaling transects (Figure V-A*1) . ' transect 1 is located at river m..e (RM) 34. 5, approximately 0. 3 mi (0.5 km) upstream of DVPS and is the Contro. Transect. Transect 2 is located approxi-mately 0.5 mi (0.8 km) downstream of the BVPS discharge structure. Transect -2 is divided by Phillis Islands the main channel is designated trant ect 2A and the back channel Transect 28. Transect 2B is the prin- l cipal ' Hon-Control Transect because the majority of aqueous discharges-from BVPS Unita 1 and 2 are released to the bac;k channel. Transect 3 4., located approximately 2 mi (3.2 km). downstream of BVPS. Sampling dates for each of the program elements are presented in Table V-A-1. The following sections of this report present a summary of findings for' each of the program elements. B. BENTHOS Objectives. The objectives of the benthic sntveys were to characterize the benthos of the Ohio River near BVPS and to determine the impacts, if any, of BVPS operations. Methods 2 Benthic surveys were performed in May and September, 1991. Benthos sampis' were collheted at Transects 1, 2A, 2B, and 3 (Figt.r e V-B-1) ,
- using a Ponar grab sampler. Duplicate samples were taken of f the south shore'at Transect 1, 2A, and 3. Saiapling at Transact 2B in the back 20,
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d POWER SDLTIGt FIGURE V-A-1 SAMPLING TRANSECTS IN THE VICINITY OF THE BEAVER VALLEY POWER STATION BVPS _ -v
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TABIE V-A-1 AQUATIC MONITORING PROGRAM SAMPLING DATES 1991 B7PS Zebra Mussel , and Corbicula Ichthyoolankton Phyto- and Month Benthos Monitoring'*J Fish Impinceinent Day Nicht Zooplankton January 18 11, 18, 25 25 February 18 1, B, 15, 22 15 2 w March 15 1, 8, 15, 22, 29 15 p. e April
~
15, 18, 19 28 19 12 55 May 13 13, 14, 17 1, 13, 14 3, 10, 31 "E 13 14 17 Q 03 w June 13, 17 7, 28 dC 11 14 29 M 34 July 12 24, 25 5, 12, 19, 26 24 25 12 bo 4k August 16 2, 9, 16, 23, 30 16 16 $b
=4 September 30 20, 25, 30 11, 12 6, 13, 20, 27 13 S O
m October 7, 31 4, 11, 16, 25 le d i Novc ber 15 5, 6 1, 15, 22, 29 15 December 12 6, 13, 20, 27 13 i (a) 2ebra Mussel and Corbicula Monitoring also includes all Impingement dates.
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i DUQUCSHC LIGitT COMPAHy l 1991 ANNUAb CNVIRONMENTAL REPORT l cnannel of l>n !131,* !aland, consisted of a single Ponar grab at the j south, middle and north side of the channel, l Each grab was washed within a U.S. Standard No. 30 sieve and the remains placed in a bottle and preserved with 104 formalin. In the laboratory, macroinvertebrates were sorted from each sample, identifi ed to the 2 lowest possible taxon and counted. Mean dentitles (numbers /m ) for each taxon were calculated for each of the two replicates and three back channel samples. Three species diversity indices were calculated: Shannon-Weiner, evenness indices (Pielou 1969), and the number of species (taxa). I IIabi t a t s Subtrate. type was- an important f actor in determining the composition of the benthic cownunity. Two distinct benthic habitats exist in the Ohio l River-near BVPS. These habitats are the result of damming, channeliza-tion, and river traffic. Shoreline habitats were generally soft muck subtrates composed of sand, slit, and detritus. An except 'n -- occu r s alona the north shoreline of Phillis Island at Transect 2A where clay t and - sand predominate. The other distinct habitat, hard subtrate, is located at midriver. The hard substrate may have been initially caused by channellration and scouting by river currents and turbulence from commercial boat traffic. Fif ty-four ~ macroinvertebrate taxa were identified during the 1991 moni-- toring program (Table V-B-1) . Species composition during 1991 was simi-
- lar to that observed during previous preoparational (1973 through 1975) and operational (1976 through 1990) years. The macroinvertebrate assemblage during 1991 was composed primorily of burrowing organisms typical of soft unconsolidated 'substrates. 011gochaetes (worms) and chironomid (midge) larvae were abundant- (Tables V-B-2, V-B-3, and lV-B-4 ) . - Common genera of oligochaetes were Limnod r ilu s, Nais, Veidovskyella and Paranais. Common genera of chironomids were Coelotanyrus, Procladius, Cryptochironomus, Polypedilum, coelotanypus, and Cricotopus. The Asiatic clam (Corbicula) , - was collected from 1974 24
-, - _ _ _ . .2_ _ --
TABLE V-3-1 SYSTEMATIC LIST OF MACROINVERTEBRATES COLLECTED IN PREOPERATIONAL AND OPERATIONAL YEARS IN THE GIIO RIVER NEAR B*NS Pr eomr eti onal Oparational 1973 1974 1975 1976 1977 1978 1979 15 83 g- 19 82 1983 1994 1995 19816 1987 1988 1989 1990 1991 Porifera . spongilla fragills X Cnidaria-Rydrozoa Clavidae Coreylophora lacustris X X X X Bydridae Crespadacusta sowertwi . X Nydra sp. X X X X I 1 1 1 X X e w
>=
Platybelminthes . ye Trieladida X X X .X Rhabdocoela F. X 5C X X X X 6k
>n Me ertea X X X X X X X X U$
Womatoda X X X X X ? X X X X X X X X X X X Qb
'C C*
- Entoprocta a~
N Urnstella gracilis X X X X X X X X X X X X X X X X X y$
-- H 3
tetoprocta X nn Federieella sp. Paludleella articulata X X X X X X X
%Q
> -J Pectinatella sp. X C" >
'Plunatella sp. X' W *C m
7 Annelida O 011gochaeta $ Acelosomatidae X X X X Echytraeidae X X X X X X X X X X X X Maldidae A11onals pectinata X Amphicheeta leydigi X X Amphicttects sp. X X Arcteonats lomondi X X X X X X Aulophorus sp. X X Chaetogaster diaphanus X X X X X X X C. diastros:etus X X X Dero digitata I X X t D. nivea X X D+ro sp. X X X X X X X X X X X X X Mats barbata X X
- n. denningi X X
- n. dretsen.ri X X X X X X X X X
- n. ec ms X X X X X X X X X
4: r s TABLE v-O-1 (Continued)
- Preoperational Cperational
. 1973 1974 1975 '1976 1977 1978 1979 1990 1931 1982 1983 1994 1985 1996 1987 1984 1999 19*0 1991-
- i. 3.(erinquis X X X -X X X
- g. perdalis I X-
. {. simpler X X- X X 1- E. vertabilis. X- X X X X
- j. Isais sp. -X I X X X .X X X ~X X' X .X' X X X X X Ophidoneis serpentina- X ,X _X. X. X X X
}- Paranais frici ,. X X- X X X X X X X X X- X X X X X X X p Paranets sp.- . X
- j. lPievettella nichleanensis- 1 Prastina idrensis. X X ,y Pristine longisama- X e
-P. osborni X X - X X X ,K 1 d P. sine X. X X X. .X' 1 X Pristina sp.
Ripistes perasita X X X X
$8 ZO g Stevine appendiculate Stephensoniene trivandrana X X
X- .I 55 U C3 X X X g Stylaria foesularis X X X- g is
-5,. lacustris X X X X Q t'* ~;
Uncinais uncineta 1 ** ** to veidoostrella intermedia X X .X X X X O m ve3dow..ve11a .p.. X
.Tubificidae. ..
EO gg Aulodtilus 11mnobius X X X X X X X X" X X X X X X >7 A. piqueti A. plurisets X X X I I X X X X X- X X X X X. -U$ Bothrioneurus veidovskyenum X X X X X X X X X X X X X X X X X gM _ y i Branebiure sowerby1 O X- X X X- X X X X X" X 4 .X X X X X X , j- Ilyodrilus templetoni X X -X X X X X X X % X k 4 Limnodrilus cervia X X X X X X X X X X X X X X X X- X
- L. cervix-(veriant). X X X X ,
I X X X X 4- L. cleperedianus X X X X' I X X X X X X X X X X' I , L. hoffmeisteri X F X X X X X X X. X X X X X X X X X X L. spiralis X X X i- L. udetemianus X X X X X X X X X X X X X X X X X X X Limodrilus sp. X Peloscolet multisetosus lonqidentus X X X X P. s. multisetosus X X- X X X X X X X X X X I' Potamothrix moldaviensis X X X P. vejdovskyi X X X X X X X Psrmnoryctades curvisetoeus. X Tubifem tubtfeu -X' X X X X- X X i Unadentified aimmature forms: with hair chaetse X. .I 1 X X X .X X X X X X X X X X X X X without hair chaette X X X X X X X X X X X X X X X X X X X
- f. Lumbricuildee . I i
. , . _ .. - - . ._ ,m .. . _ _ ,, , . _ . . . - . - . - . . -. ,,-.. . - _ _ - .-. _ . _ _ _ _ . _ , _ . . . - _ _ _ ,
~
- - v TABIE V-B-1.
(Continued)- Prooperaticma1 . Operationa1 1
- 1973 1974 1975 1976 1977 1978 1979 1990 1981 1982 1983 1984 1985 ;986 1987 1988 198e 1990 1991
, Bi.rudiraea - ]
'1Clossiphoniidee -
X nelobdella elongata X. X E. stagnolis XL seloadella,sp. X 2rpobeellidae -i X ;
- . .Ermobdella sp.
Mooraobdella sterostone' I X Art.hropoda-Ac:arina 'X X X X X X X [ X X w l Ostraco6a .
- f. 180Poda y Asellos sp.- X -
t L -Amphipode ! I, Tah tridae Byelella azteca X X X
$8~
ZO CC l '
- pn Gammaridae I Cranoonyx peeodooroci11s X, C'y f g to i Cranconyx sp. X- .
Gammerus fasciatus ' X X X < t* [' Gaaunarus sp. . X X X- X X X X X X. X X X X X X X y$ i j X g =i ! N Decapoda
- 4 - 'Collembolla X y Ephemeroptera po l '
Beptageniidae' 'X X y@ i X X > ~J Stenaeron sp. t- > Stenonene sp. X z ;
! Ephemeridae gM [
Ephemera sp. . X -> X X X X X O , Nenagente op. X 4 Baetidae X X f Ceenidae ! Caenie op. X X . X 3 Tricorythidae;- r Tricorythodes sp. X l ; Megalopters slalis sp.. X [ od_ t. [ [ Gamphidae D*omoecephas apoliatue X f Dromotamphas sp. X X X X X X Camphus sp. , Libellulidae ' X l I Libellula sp. t Trichoptera l itydropsychidee X
,} >
Chetsnatepsvehe sp. X X
'Mvdropsyche sp. X i
, . . . . ,. ,s, _
. 4 , , --,- . ., . . , - . . , - , _ - . , , , . . - . - - . . . . . . . . _ . - . - .- m, . . - .. . . . - . - - .-
l' _ g
.d j _ TABLE:V-B-1.
d1 (Continued)[
~
Prooperational' operational 1973-1974 1975- 1976 1977 19's 1979 1990 1981 1982 1983 1984 1995 1986_ 1997 1998 1989 1990 1991
~
sydroptilidae' aydroptile sp. JX. d Ourethira sp. 'X-i ,.. . Leptcceridae : l'
~
fCetaclea sp. . 1 I ..
"9ecetis sp. . X X X - X X X X- X X Polycentropodidae Polfcentropus sp. -1 X l Coleoptera X X Eydrophilidae- X Elmisee . ,
Aterronyx variegatus- X
- Dutnraphia sp. .X X~ X Be11chus sp. -X-
-Stenelmis sp.
Psephenidae' X X X. b b.
' Diptera : ..
hh
>M' Unidentified Diptera .I r -X X' I X X -X X X Fy Psychodidae' Pericosa sp.
X 1 gM
.c g Psychode sp. X **
- g Telmotoscopus sp.
Unidentitled Psychodidae pupee I h
, oo X g *3 Chaoboridae Chaoboros sp. X X X' 'I X X X gg
,,, g Simul.idae > "'s -
similium sp. X "E Chironomidae Chironominee' g*< X X , Chtronominee pupa I X X X X X X X X O Chironomus sp. X 'X X X X X- X X 'X X X X X X X X X Cladopelas sp. X X X
.Cryptochironomus sp. 'I X. X X X X X I' I X X X X X X X X X X Dicrotendipes ner n es I Dicrotendipes sp. X, X I X- X X X Clyptotendipes sp.' X X X Rarnischia sp.- X X X X X X X X X X X X X' I Micropeectra sp. X Microtendipes sp. I Parachironounus sp. X X Phaenopseetra sp. . X
'Polypedilum (a.s.) convictum type X-'
P,. (s.s.) simulans type. X
' Polypedilum sp. X X X. X X X X X X X X X. I Pheotaftytarses sp. X X X X X X X X X Stenocha romoseus sp. X* X X X Stactoctia ronomus sp. X Tanytarsus sp. I- X X X X X X X Xenocha ronomus sp. 'X I
. . . ~
, _ , _ . - . . , , , ,. .. < ,. , . _ . _ , , - , . _ , , - . . . . .. ~_._ ,..,_ ,.... _ -.m _. . . _ - . _..,.~2
.s
_ y., p'1 s TABLE V-B-1 (Continued) Preoperational Operational 1973 1974 1975 1976 1977 1978 1979 1980 1981 1992 1983 1984 199? 1996 1997 1999 1999 1990 1991 Tanypodinae' Tanypodinae pupae X X .X Ablebeamyia sp. 1 -X X X Coelotanypus scapularis I I: 1- 1 x x- x x x x. x x X x x Djalambetista puleber 1 x
.Dialmebetista sp.- X X X X Procladles_ (Procladius)
Proclad!af sp. . I 1 X X .X X X X X X X- X X X X X X X X
- . Thienema.4aayla group - X X .X X X -)
Xavreitsyta sp.- I~ 0:thocladiinae X
- 3-Orthocladlinee pupee X $
cricotopus bicinctus: I
. C. (s.s.) trifpscia Cricotopus (Isociadius) sylvestris Group I
1 g ' gn C. (Isoeladius) sp. I CC Cricotopus (s.s.) sp. X 'X X X X X X X X $$Z , Dakief f eriella sp. ' X X- X nydrobaenus sp.-
- X k" l Limnophyes sp. I j{- I
+ w Nanociadius !s.s.1 distincton x x X X x eo l to Manocladius sp. Orthoeladius sp. X X 2 X X I X X X X 1 X X
@Q 3
i Paaametrioeneous sp.,
.Parapheenocladius sp.
I I I I
$h HT Psectrocladius sp. . 1 X hh Pseuderthocladius sp. X ,y Pseudoestt M sp. X X
@ -l 1 Smittia sp. X X .. I I E f Diamesinae -
1 g is Diamesa sp. Potthestia sp.- 1 Ceratopogonidae. X: 1 I I , I I X X X X X X X , Dolichopodidae- 1 I Empididae X X 1 2 X X Wiedemannia sp.. K , Ephydridae X Muecidae X X Iumagiocidae X I X Tipulidae-
' Straticeylidae x X 1 Syrptsidae .. X t.epidoptera x x- X Moll ssca Gastroprda' Ancyllose Ferrissia sp. X X. 1 I Planorbidae 1 valwatidae'
, w*
1 l}' Ub 7tZM a c. Ze nO3TN~
*" D~ Z h*t U'c NQ 3nZ4>V = =0M4e 1
9 X X X 9 1 9 X X 9 9 1 9 n .X XX 9 _ 1 8 9 X 9 1 7 9 X X 9 1 6 6 X XX 9 1 5 9 X X 9 1 4 9 X X 9 1 4 P 3 8 X X 9 l 1 a n 2 o 9 X XX X i 9 t 1 a r 1 e 8 IX X p 9 O 1 0 6 X 9 1
- 1) 9 7 X X X
- d 9 B e 1 , - u 8 Vn 7 X XX XIX i 9 1
E. t I n 7 B o 7 X XX X AC 9 T( 1 6 7 X XXX 9 1 l 5 a 7 X n 9 o 1 i t 4 a 7 X r 9 e 1 p o 3 e 7 XX X r 9 P 1 e a d e i a i d r i e n a o h i p n S U e e r r a u u s e t t s n a a e n m s m r i m i m p m d i e u .i n d l . pd a .d r f pse r pe r e s i g si ep aa e m f f a dl i u am d u u i i t et a o i i t t al c ii r nan t n a d ui id eed o p e l w vcb si r r! es a did h ina i l d i a ib o ai p non l n v cwo rC hP p S UiA n E U lC S U e P WC
TABLE V-B-2 . MEAN NUMBER OF MACROINVERTEBRATES (Number /m ) AND PF 2 3T COMPOSITION
. OF OLIGOCHAETA, CHIRONOMIDAE, MOLLUSCA AND OTHER ORGANISMS, 1991 BVPS STATION 1
2A 2B 3 0/m 2 g ,j,2 g ,
,f,2 g gf,2 g itay 13 e
7, 3 54 95 5,759 92 5,571 88 3,707 98 ~ Oligochaeta 218 3 366 6 632 10 30 1 7 ,, Chironomidae Mollusca 30 <1 20 <1 26 <1 20 1 g, Others 158 2 99 2 126 2 20 1 %@
"E 7,760 100 6,244 100 6,355 100 3,777 101 Q r' Total NC wa w 2i g*
e !;eptember ~ 30 98 3,163 82 1,362 56 1,393 53 3,029 91 g@ Oligochaeta rg 366 9 474 19 902 35 206 6 Chironomidae 109 g* Mollusca 316 8 571 23 230 9 3 10 <1 10 1 80 3 0 0 g Others "4 3,855 99 2,437 99 2,605 100 3,346 100 Total
-=-
DUQUCSNE LIGitT COMPANY 1991 ANNUAL E!nf2 RONMENTAL RCPORT TADLE V-B-3 2 BENTil!C MACROINVERTEDRATE DENSITIES (Humber/m ), MEAN OF TRIPLICATE FOR BACK CHANNEL AND DUPLICATE SMiPLES COLLECTED IN Tile MAIN CHANNEL OHIO RIVER, 6tAY 13, 1991 BVPS
$TATI(*
Taas 1 2A 7tt 3 1 Nematoda lit $9 40 20 l Annelada , tchytteeldae 40 7 10 ' Oligochants eggs. + + + + Amphichetta Itydigj 20 gnattogaster 31sphanus 40 Nelptitetschet{ 99 7
- g. commung 109 227 40 N, . elingup $0 146 26 N. pardalls_ 1,153 237 10
.N. eleples 69
- 3. sp. _
$0 13 .
Ophidonais serpenting 7 faranals itici- 37$ 2,857 1,202 1,744 Fri stina idrensis 10 20 _P r ; stina sina 20 33 10 Pipistes persette 10 20 26 ityle d t foesularle 10 10 92 Yejdovskyella Antormedio 956 800 230 10 , _A u t od t lus 1 anob us 4 09 20 13 69 Autodt lus Egg 40 30 Autodratus p priseta 20 titanchlura gwer byl 39 10 L, anodgjy1 cet y t s 49 20 92 50 L mnoJrilus hoffaeleteri $42 460 187 L: enndtflus udekenlanus 20 10 39 10 Immatutes w/o capillifosa chaeta 4,571 128 2,377 1,035 I immatutes w/ capillitosa chaeta 493 20 fit 562 Atthropoda Acar ina - 10 Amphipoda commatue sp. 30 20 $1 Trichoptera cesactea 40, 20 Diptsaa Chironominas pupaa 10 20 chironoaus sp. 60 20 112 Cryptochtronomus ap. 10 20 Dierotendipes sp. 7 Polypedilum r.p. Its 50 407 20 Tanytarsus sp. 20 Tanypodinae pupae 20 Coelotanypus scapulatts 7 10 Procladius sp. ?6 Djalmabatista sp. 13 Cricotopus sp. 246 20 Ceratopogonida, 10 13 Mollusca > Corbicula fluminea 30 20 26 20 Total 7.760 * ?44
, a.J$b 3,777 E indlertes otgar.lsea present.
ss 32
DUQUESHE LICllT COMPANY, 1991 AHkUAL EtNIBOtlHEllTAL REPORT TABLE V-B-4 BENTHIC MACR 0 INVERTEBRATE D?.NSITIES (Number 2/m ), MEAN OF TRIPLICATE FOR BACK CilANNEL AND DUPLICATE SAMPLES COLLECTED IN Tl!E R\IN CliANNEL OHIO RIVER, SEPTEMBER 30, 1991 l DVPS STATION Taxa 1 2A 2B 3 i Platyhelminthes l Tricladida cora spi 7 Ilenestea , 30 Hematoda 10 1 Entoprocta urnatella Sracills
- Annelida Echytraeidae 10 I 011gochaeta eggs * * *
- Hals communis 128 10 20 306 I Hals sp. 7 PJittina idtensig
- 20 89 Pristina osborni 187 119 286 styleria fossularis 10 10 108 Autostilus llenob us 10 49 164 30 AutodriluP piquet; 30 184 20 Autodrinus plurisete 13 20 ersnehtura sowerbyl 20 30 L anodritus cerviu 59 10 60 L anodrinus hoftneistert 227 197 72 345 1.lanodritus udekenlanus 89 53 10 1 Immatures w/o capilliform chasta 2,305 897 781 1,498 lanatures' w/ cap!!!!! ora chasta 138 20 79 227 Arthropoda
- Acarina 46 T6tchopters Oecells sp. 20 Diptera-Chitcaosinit pupae 10 7 ,
chieontmos sp. 20 33 20 'i cryptochironomus sp. 89 148 20 Dierotendipes sp. 7 Polypedilua sp. 148 237 283 89 Tanytarsus sp. 49 164 Menochironomus sp. 30 l Coelotanypus scapularis 99 243 19 l Paocladius sp. 10 138 10 l- Cricotopus sp, 7 Hanocladius sp. 10 l l . Mollusca l Pelecypoda
.Corbleula fluminea. 276 571. 230 109 j Pistelun ap. 10 Unionidae Unionidae tamature 30 Total 3,855 2,437 2,605 3,346
+ Indicates organisms present.
33
. =- __ - _. . _- - --
DUQUCSNE LIGHT COMPANY 1991 AlmuAb ENVIRONMENTAL REPORT through 1978, and 1911 through 1991 surveys. None were collected in the 1979 or 1980 surveys. No unusual or unexpected species of benthos were encountered durlag 1991 nor were any threatened or endangered species collected. Community Structure and Spatial Distribution 011yochaetes accounted for the highest percentage of the macroinverte-- brates at all sampling stations in both May and September (Figure V-B-2). Density and species composition variations observed within the BVPS study area were due primarily to habitat differences and the tendency of certain types of macroinvertebrates (e.g. , oligochaetes) to cluster. Overall, abundance and species composition throughout the study area were similar. In general,_ the mesn density of macroinvertebrates during 1991 was lowest at Transect 3 in May and 2A in September. Higher mean densities
- usually occur at Transects 1, 2B, and 2 where substrates near the shore were composed of sof t mud or various combinations of sand and silt. The - lower abundance at Transect 2A was probably related to substrate condi-tions (clay and sand) along the north shore of Phillis Island.
Comparison of Control and Non-Control Station 4
.No adverse impact to the benthic community was observed during 1991.
This conclution is based on a comparisoa of data collected at Transect 1 (Control) and 2B (Non-Control) and on analyses of species composition and densities. Data indicate that oligochaetes were usually predominant throughout the study area (Figure V-B-2). Most abundant taxon at Transects 1 and 2B in both May and September was immature- tubificids without capilliform chaetae ' (Tables V-B-3 and V-B-4) . In May, the oligochaetes which were 34
PERCENT COMPOSITION
'**~
- -, G
* ~ s i
*~ .. m 55 o< . . , , ,'.
. . f. . .
, t , 43 r+ r , ,,
PREOPERA IONAL YEARS OPERATIONAL YEARS I I CHIRONOMIDAE tm I ALL OTHERS E OLIGOCHAETA FIGURE V-B-2 IN E OI O RIVER 77EA BVPS URIhG PREOPERATIONAL AND OPERATIONAL YEARS
DUQUESNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT common or abundant at both stations were Limnodrilus hof(meisteri, Vejdovskyella intermedia, and Paranais g el,. In September, the cligo- l chaete Limnodrilus hoffmeisteri, the midge Polypedilum, and the clam Corbicula fluminea were the common organisms collected at both stations. In May and September 1991, a greater diversity of organisms were col- l 1ected at No.1-Control Station 2B than at Control Station 1 (Table V-B-5). This has occurred reveral times during past surveys. The mean number of taxa and Shannon-Weiner indices for the back channel were within the range. of or exceeded the values observed for other stations in the study area. ' Dif f erences observed between Stations 1 (Cont ;ol) and 2B (Non-Control) and between other' stations could be related to dif f erences l'a habitat. . None of the differences were attributed to DVPS operat4on. [omparison o of Preoperational and Operational Data
- Composition, percent occurrence and overall abundance of macroinverte-brates has changed little from preoperational years through the current study year. 011gochaetes have been the predominant macroinvertebrate in the community each year, and they comprised approximately 86% of the individuals -collected in 1991 (Figure V-B-2). A similar olig ochaete assemblage has been reported each year. Chironomids and mollusks have composed most of the remaining f rac tions of the community each year.
The potential nuisance clam, Corbicula, increased in abundance from 1974 9 through 1976, but declined in number during 1977. Since 1981, Corbicula have been collected - in the benthic surveys including 1991 when their densities - were several times greater in September as compared to those - found in May. Total macroinvertebrate densities for Transect 1 (Control) and 2B (Non-Control) for each year since 1973 are presented in Table V-B-6. Mean densities of macroinvertebrates gradually increased from 1973 through 1976 (DVPS Unit 1 start-up) to 1983.- In 1991, densities were slightly lower at Transect 2B than those at Transect 1. These lower densities at 3,6
DUQUESNE LIGilT COMPANY 1991 ANNUAL EIN!RONMENTAL REPORT TABLE V-B-5 ; MEAN DIVERSITY VALUES l'OR DENTHTC MACR 0!!NERTEBRATES COLLECTED IN THE OHIO RIVER,1991 l BVPS l l STATION j 1 2A 2B 3 l DATE: May 13 l No. of Taxa 17 21 19 12 I
. I Shannon-Welner Index 2.00 2.91 2.84- 2.03 i
Evenness 0.50 0.72 0.72 0.59 i DATE: September 30 No. of Taxa 16 13 13 15 Shannon-Welner Index 2.29 2.66 3.04 2.69 Evenness , 0.58- 0.74 0.85 0.68 i O P b F .. 37,
s
' TABLE V-D-6 BF74THIC MACROINVERTEBRATE DENSITICS (Number /m ) FOR STATION 1 (CONTROL) AND STATION '2B '(NON-CONTROL) DURING PREOPERATIONAL AND OPERATIONAL YEARS BVPS Preoperational Years operational Years 1973 1974 1974 1976 1977 1978 1979 1980 Month 1 2B 2 2B 1 2B 1 2B ) 2B 1 2B 1 2B 1 2_B January Februarr 20$ 0 703 311 358 200 312 .1.100 1,499 2, 54 5 1.C29 1,296 -
e w March 425 457 *=* TO April ZC 2o CC May 248 . 508 1,116 2,197 927 3,660 674 848 351 126 1.004 840 1.041 747 >M-C- b1 Z June 5 . 40 507 686 Q t1
&V M ~
July 653 119 421 410
- tr O
-W -
C2 August 99 244 143 541 1,047 1,124 851 785 391 3.474 6c1 1,896 1,195 588 Q g '=3 MO Septent er 175 92 1,523 448 $Q
>5 Octo+>et 2 56 239 FE Newember 149 292 318 263 75 617 388 1,295 108 931 386 1,543 812 806 5 y
O December $ neon 231 206 463 643 546 671 631
- 1,485 421 1. $88 709 1,52t 857 673 1,198 330 e
a- >
.m 4 .-, s y
l . . . . . . . . . . .. TABLE V-B-6 (Continued)' OMrational Yeare 1991 1982 1951 19se toss 1g86 1987 19se 2B 2e - 1 28 - 1 2B 1 2B 1 2B 1 2s 1 23
^ncm th 1 1 my 209 456 3,490 3,026 3,590 1,314 2,741 . 621 2,254 867 601 969 971 2,649 1,804 1,775
'2,185 112 2,956 .3.364 4,172 4,213 1,341 828 1,024 913 349 943 2.910 2,760 1,420 1, 514 gepten wr 1,197 684 3,221 3.195 3,tel 2,764 2,041 - 725 1,640 890 725 9 56 2,440 2,714 1,612 1,645
. Mean s.*
w w e EU eparational 7 ears gj 1999 1990 1991 CC Month .. 1 25 1 2E 1 25 [M E"
< t*
May 3,459 2,335 15.135 .5,796 7,760 6,355 y 8' s2 "= septe=*r l',560 4,212 s. 550 1,11: 3.e55 2,605 g MO 5,808 4,480 gO nean 2,510 3,274 10,343 "3.457
>k c- >=
t O k w
DU90CSNC b! Gilt COMPAMv 1991 ANNUAL ENVIRONMENTAL REPORT Transect 2B in 1991 were well within the range of previous data from preoperational and operational years. Mean densities have frequently been higher in the back channel of Phillis Island (Non-Control 28) when compared to densities at Transect 1 (Control). In 1991, and in years such as 1990, 1985, 1984, 1983, and 1979, when mean densities were lower at Transect 2B than at Transect 1, the differences were negligible.
]
These dif ferences could be related to substrate variability and random-l ness of sample grabs. liigher total densities of macroinvertebrates in the back channel (Transect 28) when compared to Transect 1 was probably due to the morphology of the river. Mud, silt, and back channel areas I were predominant at Transect 2B creating conditions more f avorable for burrowing macroinvertebrates in empari son to Transect 1, which has little protection from river currents and turbulence caused by commer-l cial boat traffic. l Summary and Conclusions Substrate was probably the most important factor ce'. olling the distri-bution and abundance of the benthic macroinvertebrates in the Ohio River near BVPS. Sof t muck-type substrates along the shoreline were conducive to worm and . midge proliferation, while limiting macroinvertebrates which require a more stable bottom. At the shoreline stations, Oligochaeta accounted for 86% of the macrobenthos collected, whereas Chironomidae and Hollusca each accounted for about 94 and 51 respectively. Community structure has changed little vince preoperational years and there were no indications that BVPS operations were af f ecting the ben-thic community of the Ohio River. C. PHYTOPLANKTO3 Objectives Plankton sampling was conducted to determine the condition of the phyto-plankton community of the Ohio River in the vicinity of the $ x ' 49
Ww _ DUQUEstiE LIGHT COMPAliY 1991 At1NUAL E11VIRONMENTAL REPORT Methods One entrainment sample was collected monthly. Each sample was a one-gallon sample taken from below the skitraer wall from one operating intake bay. This nne-gallon sample was preserved with Lugol's solution and war used for the analyses of both phytoplankton and zooplankton. In the laboratory, a measured aliquot of the sample was settled in an inver:ted microscope chamber. A minimum of 250 cells were identified and coun:ed at 400X magnification. For each collection date, the volume of sample settled and examined was adjusted depending on cell density. A Hyrax diatom slide was also prepared monthly from each sampl e.. This slide was examined at 1000X magnification to make positive identifica-tion of the diatoms.
- Densities (cells /ml) , Shannon-Weiner (log base 2), and evenness diver-sity indices (Pielou 1969), and richness index (Dahlberg and Odum 1970) were calculated for each monthly sample.
Seasonal Distribution Total cell densities of phytoplankton from stations on the Ohio River and in the intakt samples have been similar during the past years (Annual Environmental Reports 1976-1990). Species composition has also been similar in entrainment samples and those from the Ohio River (DLC
); 1980). Therefore, samples collected from the intake bays should provide an adequate characterization of the phytoplankton community in the Ohio River.
i During 1991, the January through March samples had phytoplankton densi-ties of 703 to 1,332 cells /ml (Table V-C-1 and Figure V-C-1) . Total mean densities increased each month from April to July when the annual maximum of 55,908 cells /ml occurred. Total densities decreased to 35,139 cells /ml in August then slightly increased to 38,089 cells /ml in September. After September, densities displayed a general decreasing 41
TABLE U-C-1' MONTHLY PHYTOP2ANKTON CROUP DDISITIES (Number /ml) AND PERCENT COMPOSITION FROM ENTRAINMENT SAMPLES, 1991 BVPS Jan Feb' Mar Apr MaY Jun Group' t/ml % f/ml 1- t/ml % t/ml % 3/ml % t/ml t Chlorophyta 39 6 20 3 55 4 410 4 4,383 26 1,929 5 Chrysophyta 179 25 ~150 21 260 20 7,905 69 7,112 43 6,869 16 $ Cyanophyta 15 2 0 0 74 6. 0 0 0 C 32,620 76
~
Cryptophyta 33 5 11 6 39 3 336 3 854 5 283 1 E3 l Microfhagellates Other Groups 437 0 62 0 511 0 71 0 903 68 2,740 24 4,342 26 994 2 58 1 <1 0 0 0 0 9 <1 $ nn 4 Total 703 100 722 101 1,332 101 11,391 100 16,691 100 42,704 100 5 e-a N 55 82i Jul Aug Sep Oct Nov Dec h ry Group g/ml % 9/ml % 9 /ml- h f/ml 1 8/ml 1 t/ml 1 5@ Chlorophyta' 3,986 7 5,549 16 3,774 10 3,354 13 4,638 28 120 10
$5
,e5 l
Chrysophyta 4,493 8 3,213 9 7,502 20 9,028 34 6,2 r 37 394 34 y Cyanophyta 39,847 71 23,603 67 21,577 57 8,703 33 530 3 93 8 3 Cryptcphyta 5,485 10 776 2 619 2 302 1 500 3 28 2 Microfhagella tes 2,070 4 1,989 6 4,590 12 5,108 19 4,840 29 530 45 Other Groups 27 <1 9 <1 27 <1 0' O O O 'O O Total 55,908 100 35,139 100 38,089 101 26,495 100 16,760 100 1,165 99
Mi.
- i; CELLS / MILLILITER 100000 r - , _ _ ,
r _. ~o _ ./ W.
' 4 \
- ~
10000 y_ 1 g j ,/ j ___w N ( ---- J
/ \
~
g N TN \ ,
/ \ // ' - /
3 1000 - h f \'
-+
y
$g g
gg c
-U a j cy
/ _
J nn
# 2e k I i*5 0 100 . _ _ _
gl as
>2
. _ . egI
-. g<
a
' ' ' ' ' ' ' ' ' 5 10 JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC MONTH
+ PREOPERATIONAL YRS. I iwERAGE 1976-1990 0 1991 FIGURE V-C-1 MONTHLY PHYTOPLANKTON DENSITIES IN THE OHIO RIVER DURING PREOPERATIONAL (1974-1975) AND OPERATIONAL (1976-1991) YEARS BVPS
DUQUCSNE 1.!Gili COMPAllY , 1991 ANNUAL ENVIRONMENTA!, REPORT trend to a low of 1,165 cells /ml in December (Table V-C-1 and Figure
.V-C-1).
During the months with cool temperatures, microflagellates, and d' atoms (Chrysophy ta ) , were generally the most abundant groups of phytoplankton during 1991 (Table V-C-1 and Figure V-C-2) . Blue-green algae dominated , the pnytoplankton community during the low flow conditions and very warm temperatures of June, July, August, and September of 1991 when relative percentages of occurrence for Cyanophyta ranged f rom 57% to 76% of the total phytoplankton. Green algae (Chlorophy ta) developed populations of 26% to '2 0 % in May and November during 1991. Relative abundance of Cryptophyta was highest in July (104) (Table V-C-1). Diversity indices for the phytoplankton during 1991 are presented in Table V-C-2. Shannon-Weiner indices ranged f.om 1.43 to 3.52, evenness values f rom 0.32 to 1.73, and richness values f rom 1.82 to 3.36. liigh (22.00) diversity values occurred in 8 of the 12 months. The lowest value for Shannon-Weiner Index occurred in April when diatoms dominated the cell . counts; however, the lowest number of species occurred in February when microflagellates were predominant. liighest number of taxa (35) occurred in September. Phytoplankton communities f rom June through October were dominated by Microcystis incerta. During the remainder of 1991, microilagellates and centric diatoms were the most abundant taxa (Table V-C-3) . Many blue-green algae populations such as Microcystis. are favored by the hot weather and low turbidity conditions that were- prevalent in the region of the Upper Ohio River during the summer of 1991. Microcystis incerta is a colonial algae that contains relatively low numbers of minute cells in-each colony. It seldom causes nuisance conditions such as surf ace scums on the water. l l 1. 44,
i: CELLS / MILLILITER i 100000= -- =.= me_=_= = u =gg _ __ .==ym rA - V M 1 10000
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1 i r i r r i i i i 4 i i g JAN FEB MAR APR MAY JUN 'JUL AUG SEP OCT MOV DEC $. MONTH 4- CYANOPHYTA CHRYSOPHYTA .
^
CHLOROPHYTA 4- CRYPTOPHYTA & MICROFLAGELLATES FIGURE V-C-2 i PHYTOPLANKTON GROUP DENSITIES FOE ENTRAINMENT SAMPL4S, 1991 BVPS
2 -
~ TABLE V-C-2 -- '
' PHYTOPLANRf0N DIVERSITY INDICES BY. MONTH .FOR ENTRAINME2iT SAMPLES, '1991 -
BVPS-Jan Feb Mar- Apr __May Jun No. of Species 16' 15 20 18 28 23 Shannen-Weiner Index 2.21 .l.71 1.90 1.43 3.52 1.44 Evenness 0.55 0.44 0.45 0.34 0.73 0.32 ~ Richness
'2.29 2.13
.2.64 1.82 2.78 2.06
- E o .: .
25 9 8 :.
.- t~ tn Jul Aug Sep Oct Nov Dec 'X g; No. of Species 29 32 35 24 29 25 25 t- -
g5 $ 8N Shannon-Weiner Index '2.31 2.89 2.70 2.68 '3.45 3. 2'. 2.46 @f z o-- Evenness 0.48 0.58 0.53 0.58 nx. 0.71 0. '. is 0.53
;C g ,
Richness 2.56 2.96 3.22 2.26 2.88 3.36 2.58 h O-k
- a. .y - - _ - - - - - - -
wA
, c c s ,
r #
.in. -' t,un--,
2
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~
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' TABLE V-C-3=
E -
~
DENSITIES ('fusaber/mif OF MOST. ABLMDM ' 'KTU dXA f (Fif teen Most Abundant?on : m COLLECTED FROM ENFRAINMEtn - JANUARY THROUGH DECDBER. BVPS-
- Jan ' reb' Mar h- h Jun Jul - Augo Seg : M h-- ' g:
CTANOPHYTA' Lynebyelinnettea- ,
" 31 1 ~'
- Moriamopedia tenuissime' - 3,312 10,343 . ;3,264 Microcystis incerts - 74 32,620.. 35,500. - 12,862' 18,156 8,703 Deci11storia linnetica .15 .621 199 102 530L _ C2 y -'
Coccoid cyanophyta (S g. - 414 CELCet0PBYTA Actinastrum hentaschii '30 ' 88 ~ 199. 568 : Ankisirodessus convolutus,._ 1 1 3 5 27 46 - 64 < 200 173 328' " y 31 l ,@ $I Antistrodessus Kaicatus 3 17. : 32 . ' 637 200 46 9 36. 73 .le2 ~f20 > t5s Chlorophyta I ~ [ Ctalamydamonas spp. 7 7- 360 662. 332. 1,035 530 204 51 0
; 189.'
- 946 66; 729,'
5" $:
. tg M -_
~J Dictyosphaeritas pulebeitum 883 796 310 265 408 ' 1,061 ' ..k p l$
lagerheisia genevensis . 74 265 189 199
-3 .- Micrectinium pusillum . 237' 510 ,
" S" '
- q Monoraphidium cireinale :368 1,061- 473 '796 '
2 309 Mougeotia spp. . 146 36
- go Scenedessus acuminatus .4 4 7 18 73 ' .36 82 7. --
g Q? 2 Scenedessus bicellularis 88 736 2,277 1,193. 204 - 189 133 42 >m-
;- Scenedessus biiuga 30 I$'
- Scenedessus quadricau6a 4 36- 36 18 2fA 237 246. 91 - g *< <
selenastrum minutus- 102 199 10 ,o Spermatosoops1a erultens : 1 1 2 - O Tetrastrum he5tacanthus dO8 4 Unidentified chlorophyta colony 177 1,591 796 b
.p
. -j r
s
- vis' 7y '""r-WJ-7 p S' W t Wy a+@1- 4- ') Y 'ks *<--w"9 'w- M-
TABLE V-C-3 (Continued)
'Jan Feb . Mar g g Jun Jul M 5,*E M Nov DN-CHRYSOPHYTA Achnanthes stinutissima 15 21 104 Asterionella formosa_ 37 35 37' 133 1,987 53 0 125' Diatana vulgare 5 Dinobryon sertularia 2 5 228 64 Gosphoness olivaceum 1$
Melesira ambigua 32 1,046 682 73. 191 455 '82 18 Melosira distans 464 55 182. 328 218 437 400 7 Melosire varians . . 4 3 16 36 [ Navicula cryptocephala 5 17 22 25 9 4- w 44 "' Navicula viridula 7 30 7' Nittschia acicularis 442 133 3P t7 Nitzschia fonticula 31 kh Mit2schia holsetica 1,346 133 g Q. Nitzschia pales 31 t- (A Skeletonesa potamos 221 862 207 729 816 378 994 _ Q Stephanodiscus niagarne~~ ' 199
- Synedra nana 7 5 74 199 - 10 IC Synadra rumpens 15 10 m9
$ synura uuella 5 9 -3Q
, Small centrics 52 70 141 7,691 3,459 4,707 1,863 1,724 6,120 7,663 3,779 ics gg 2C CRYPTOPHYTA y@ Cryptormonas erosa 3 5 9 25 118 18 2,070 173 82 18 - 27 7- c* g cryptorsonas marisonii 1 2 1,863 73 27 9 .: y Rhodomonas minuta 30 35 ~30 309 736 265 1, 552 530 51 0 284 464 21 h
*e O
MICROFIACELIATES 437 511 903 2,740 4,342 994 2,070 1,989 4.590 5.108 4,840 530 g Total Phytoplankton 703 722 1,332 11,391 16,691 42,704 55,938 35,139 38,089 26,495 16,760 1,269 Total of Most Abundant Taxa 703 718 1,331 11,391 16 390 42,304 55,377 14,405 37,350 26,128 16,640 1,212 P2resnt Corsposition of Most 100 99 100 100 99 99 99 98 ' 98 99 99 96 Abundant Phytoplankton
DUQUCSNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT I l Comparison of Control e'i Non-Control Transects
?lankton samples were not collected at any river stations after April 1, 1980, due to a reduction in the scope of the aquatic sampling program; therefore, comparison of data was noi. possible in 1991.
Comparison of Preoperational and Operational Data The seasonal succession of phytoplankton varied f rom year to years but in general, the phytoplankton taxa have remained consistent. Phyto-plankton communities in running waters respond quickly to changes in water temperature, turbidity, nutrients, velocity, and turbulence (Hynen 1970). The phytoplankton frcv the Ohio River near BVPS generally exhib-ited a bimodal pattern of annual abundance. During the pteoperational year 1974, total densities peaked in August and October, while in opera-tional yests 1976 through 1979; mean pekk densities occurred in June and September (DLCo 1980). Total phytoplankton densities in 1991, displayed a bimodal pattern when peaks occurred in July and September. The devel-opment of phytoplankton populations during 1991 was undoubtedly influ-enced by the hot weather, low rainfall, low turbidity and low water levels which f avor phytoplankton growth and cycles (Hynes 1970). Although the phytoplankton development in 1991 was enhanced by varm temperatures and low turbidity levels, the speci es' composition was similar to those of other preoperational and operational years. No major change in species composition or community structure was observed during 1991. The differences in the phytoplankton community between 1991 and the previous years were due to natural fluctuations and were not a result of BVPS operations. Shannon-Weiner, evenness, and richness diversity values were similar to those usually observed for an annual cycle of phytoplankton near BVPS. This was primarily due to the dominance of centric diatoms and micro-flagellates which have been frequently the most abundant algae during the winter, spring, and fall months in the Ohio River near BVPS. Yearly mean Shannon-Weiner diversity indices f rom 1973 ~rhrough 19?1 were simi-49 l l
DUQUESNE LIGilT COMPANY. 1991 ANNUAL ENVIRONMENTAL REPORT lar- ranging from a low- of 2.01 in 1990 to a maximum of 4.30 in 1982.
.The-Shannon-Weiner diversity indice of 1991 was 2.46. This value was similar - to the previous mean Shannon observed in 1973 of 2.38 (Table -V-C-4). The yearly mean evenness value- of 0.53 was within the range of those observed in-the past. From 1974 through 1990, all evenness values ranged from 0.27 to 0.90. The maximum wenness diversity value is 1.0 and occurs when each species is represented by the same number of individuals. The mean number of taxa each year ranged from 19 in 1973 to 49 in 1986. (25 in 1991) . The highest number of taxa (68) in phy to-plankton samples occurred during November of operational year 1986.
Summary and Conclusions The . phytoplanktre community of the Ohio River near BVPS exhibited a slightly modified- seasonal pattern compared to those observed in previ-ous years. This pattern although different f rom other years for the Ohio River near BVPS is common to temperate, lotic environrents that experience frequent warm water and low turbidity conditions. Total cell densities , were within the range observed during previous years.
~
Although blue-green algae dominated the phytoplankton during the summer, the species' composition ' remained similar to that of the previour ears. Diversity indices were within the range of those previously observed near BVPS. D. ZOOPLANKTON Objectives Plankton - sampling was conducted to determine the condition of- the zoo- i plankton community of the Ohio River in the vicinity of BVPS and to assess possible environmental ' impact to the zooplankton due to the operation of BVPS. 50
.a
m .1! TABLE V-C-4 PHYTOPLANKTON DIVERSITY INDICES -(MEAN OF ALL SAMPLES 1973 TO 1991) - NEW CUMBERLAND POOL OF THE OlhO DIVER DVPS Apr ~May Jun g g Sep_ Oct Nov _. o.e x Jan Feb Mar 1973 24 17 16 19 2 (d) 13 24 27 28 30 Number of Species 7 No 3.37 3.25 3.27 2.38
- 0. 54 0.63 1.64 2.28 3.55 3.72 Shannon Index(at 1.55 0. 52 Sample 0.50 0.54 0.53 0.38 0.33 0.15 0.11 0.25 '0.35 0.55 h enness 2.63 3.17 3.61 3.46 3.24 2.89 2.80 2.48 Richness 1.24 0.29 1.50 1974 60 34 47 34 y 8 17 22 44 46 47 Number of Species 12 4.03 4.25 3.85 5.02 3.83 us 2.96 2.23 3.18 3. 50 4.89 4.40 Shannon Inder 0.57 0.58 0.62 0.62 0.56 0.55 0.54 0.58 0.56 f henness 0.55 0.46 4.77 5.44 4.43 j Richness 2.55 1.82 3.05 3.74 5.56 5.45 5.46 6.49 go
*C ZC 1975 Number of Species 52 34 43 32 40 40 h$
- 4. 53 4.22 4.37 4.22 4.48 4.36 0'< !S Shannon Inden 0.80 0.83 0.01 0.87 0.85 0.83 r2 5 h enness 5.57 3.96 4.98 3.92 6.19 4.91 {p Richness --
MO j 1976 Number of Species 31 35 31 38 47 49 46 43 38 3.93 33 4.16 35 4.24 38 4.45 39 4.19 hk gn 4.36 3.90 4.25 4.14 4.27 4.28 4.30 Shannon Index 3.98 0.75 0.83 0.83 0.85 0.90 ZO 0.85 0.78 0.81 0.75 0.76 0.78 0.80 hennes s 0.80 4.34 3.85 4.17 ( 95 5.79 4.83 Richness 5.15 5.89 4.92 4.10 4.68 4.79 4.72 $ k :! en 197) Number of Species 20 28 31 24 36 30 44 39 37 32 33 4.12 27 32 .)n o Ql !
- 3. 52 4.36 4.26 4.29 3.92 4.00 3.64 3.31 3.00 2.78 4.16 Shannon Inden 1.96 0.70 0.61 0.60 0.80 0.72 0.80 0.81 0.82 0.78 0.82 0.83 0.73 $ !
henness 0.44 4.26 3.87 3.98 4.18 3.72 3.84 3.14 4.57 4.44 2.95 3. 53 2.77 4.63 Richness l 1978
- 37 .35 37 34 32 35 29 32 42 28 42 36 Nesber of Species 37 4.17 3.81 3.99 3.80 4.44 3.99 4.08 3.68 3.77 4.67 3.30 4.16 3.95 Scannon Index 0.78 0.77 0.80 0.76 0.77 0.76 0.* e.,8 Ev ennes s 0.78 U.76 0.76 0.87 0.69 R1chness M 1979 24 29 25 28 36 27 19 36 34 27 34 Number of Species 18 16 4.12 4.07 3.68 4.32 3.80 3.36 3.79 3.22 3.78 3.84 4.10 3.88 Shannon Inder 3.49 0.84 0.84 0.88 0.77 0.83 0.81 l 0.84 0.82 0.88 0.62 0.74 0.81 0.a0 h enness 7.72 3.26 3. 52 3.57 5.19 3.54 2.64 3.36 4.69 4.08 2.98 3.46 Richness 2.97 (
1980 (c) 16 32 24 33 37 24 24 25 21 18 30 Number of Species 28 18 4.10 3. 54 3.73 4.56 3.57 3.78 3.82 3.28 3.26 3.61 3.45 Shannon Indez 3.88 2.64 0.82 0.77 4.74 c.87 0.78 0.83 0.82 0.75 0.78 0.74 0.86 henr.ess 0.81 0.64 1.94 3.33 2.59 4.01 5.40 3.15 l 2.65 3.49 4.02 2. 50 2.J8 2.90 Richness 4.07 I
' ~'
- < ,A
, .y 4- "
1 TABLE U-C -. (Continued) - Jan . 3bi Mar Apr May . Jin 'Jul- Aug Sep Oct Now w $ 1981-Number of Species 22 3? 37' 39 34 ' 33 '33 ' $1 35 . 27 40' 32 35 Shannon Index T3.92 ..J -4.39 2.29 3.6f '4.56 4.13' '4.59 4.07- 3.90 4. 00 .. 4.32 '3.95:
. D enness 0.88 3.45 - 0. 8 4 _ c.43- 0.72 0.90 0.82 0.81 0.79 0.82: .0.75 0.86' O.794 Richness 3.91 3.84 6.10 4.58' ?.69 4.61 '3.73 5.76 3.85 3.56 5.00 4.55 4.60 -
1982 ' Naber of Species 51. '41 = 46 - 22 55 .45 66 . 54 53 35 50 49 -4 7 -- Shannon Index- 4.68 :4.80 -4.96 1.88 4.79 4.33 4.72 4.54 4.22 -3.97 -4.09 '4.66 4.30 h enness '0.82- 0.90 0.90 0.42 0.83. 0.79 0.78 0.79 0.74 0.77 0.72 0.83 0.77-Richness 7.17 6.43 6.88 2.36' 6.15 4.96 6.65' 5.33 5.23 3.61 5.36 6.23 5. 53 E e 1983 w Number of' Species .36 42 51 52 25 42 37 , 40' 37 45 37 52 41 pn Shannon Index' 4.27 4.01- 4.60 4.74 3.67 4.41 4.16 4.28- 3.56 3.51 4.17- 4.72 4. l a' 4c-henness 0.82 0.74 0.81 0.83- 0.79 0.82 0.80 0.80 0.69 0.64 0.80 0.83 O 0.78 cc Richness 5.17 6.45 7.35 6.64 2.98 4.1s 3.63 4.17 3.83- 4.46 4.38 6.48 4.98- yy 1984
=
M 2 tu . Na ber of Species 31- 60 36 . 46 41 51 . 57 54 51 53 54 44 48 : <: ta Shannon Index 4.02 4.89 4.30 3.06 4.37 4.48 4.34 4.03 4.38 4.00 4.59 4.10 4.21 y3 m h enness 0.80 0.83 0.82 0.55 0.81 0.79 0.74 0.70 0.77 '0.70 0.80 0.75 0.76' ~Q: . N Richness 5.05 8.95 6. 54 6.98 5.55 6.41 .7.29 5.97 5.43 5.70 7.10 6.71 6.47 3 t1 0 1985 41 38 46 M$ Number of Species 53 39 52 53' 58 50 61 50 39 48 . g y-Shannon Index 3.80 3.31 4.44 3.88 4.24 2.95 4.16 4.24 3.59 2.57 3.15 3.26 3. 56 2: henness Richness 0.71 6.42 0.63 5.75 0.78 8.48 0.56 5.25 0.77 4.71 0.52 5.12 0.72 6.83 0.73 6.14 0.63 5.40 . 0.43 6.09 0.55 6.70 0.61 5.88 0.64 6.06 as
'f O
- U 1986 . *3 Naber of Species 31 39 42 34 45 60 56 48 60 54 68 O 49 Shannon Indes 3.79 4.48 3.73 1.50 4.04 3.78 4.04 3.94 4.21 4.01 4.44 4.40 3.86 Evenness 0.57 0.85 0.69 0.29 0.74 0.64 0.69 0.70 0.71 0.70 0.73 ' C.:79 0.69 Rienness 4 . 54 6.40 6.32 3.72 4. 54 7.37 6.20 4.75 5.96 6.34 9.58 7.99 6.14 1937 Nussber of Species 42 44 29 33 33 36 50 39- 33 36 35 31 37 Shannon Index 2.99 2.28 2.51 1.89 3.38 3.56 3.76 3.44 2.12 2. 52 2.54- 2.41 2.78 Evennes s 0.55 0.41 0.52 0.37 0.67 0.69 0.67 0.65 0.42 0.49 0. 50 0.48 0.5J-Richn ess 5.24 5.58 3.24 3.71 3.36 3.67 4.80 3.77 3.11 3.93 3.80- 3.79 4.00
, . _. ,_ _ - - _______m_________..a
1 P TABLE V-C (Continued) Jan Feb ~ Mar Apr May Jun Aug Sep Nov'
.Jul Oct _Dec' X 1988 Number of Species 31 34 27 40 45' 26 42 42 37 37- 36 27 35' Shannon Index 3.20- 1.90 1.72 2.68 2.83 2.88 3.76 3.13 3.76 2.30 2.61 2.65 ~ 2.78 Evenness 0.64 0.37 0.36 0. 50 , 0.51 0.61 0.70 0.58 0.72 0.44 0. 50 0.56 0.54 '
Richness 3.43 4.21 3.28 4.65, 4.75 2.66 4.20 4.12 3.70 3.25 3.83 3.00 :3.76 so . 1989
- Number of Species 27 46 25 45 26 25 ~37 29 24 30 34 29 31 Shannon Index 1.36 4.32- 2.00 3.26 1.81 '2.11 2.80 3.01 3.70 3. 53 2.16 1.95 2.67 yb-brenness 0.29 0.78 0.43 0.30 0.38 0.45 0.54 0.62. 0.81 0.72 0.42 0.40 0.54 Richness 2.96 6.12 3.16 5.74 3.33 2.85 3.73 3.11 2.85 3.34 4.07 3. 53
>m 3.73-C* L1 7.
1990 to t'2 - Number of Species 27 , 22 20 25 32 29 Shannon Index 1.58 1.22 2.49 1.69 1.99 2.64 26 1.71 33 2.41 30 2.70 25 1.50 21 34 27 k t* 1.99 2.22 2. 01 -- Evenness 0.33 0.27 0.58 0.36 0.40 0. 54 0.48 0.32 0.36 0.55 0.45 0.44 0.42 h" b" -{ Richness 3.45 2.67 2.11 2.80 3.32 3.00 2.69 3.32 3. 52 2.94 2. 52 4.16 3.04 y9 mo 139) Number of Species 16 15 20 18 28 23 29 32 35 24 29 25 25
> "o Shannon inder 2 'l -1.71 1.94 1.43 3.52 1.44 2.31 2.89 2.70 2.68 3.45 3.27 2.46- "$
Evenness 0.L5 0.44 0.45 0.J4 0.73 0.32 "0.48 0.58 0. 53 Richness 2.29 2.13 2.64 1.82 2.78 2.06 2.56 2.96 3.22 0.58 2.26 0.71 2.88 0.70 3.36 0.53 .g k 2.58 .o o I*I Snannon-Weiner Index tbjNo data (c) Data for period' April 1980-December 1991 represents single entrainment samples collected monthly. (dl Blanks represent periods when.no collections were made. a
i' DUQUCSNE LIGHT. COMPANY 1991 ANNUAL ENVIRONiCNTAL REPORT l 1 Methods. ' The-- zooplankton analyses were per formed on one liter aliquots taken f rom the preserved ' one-gallon samples obtained from the intake bay. (See Phytoplankton methods, in Part C). - One liter f rom each sample was fil- , tered through a 35 micrometer (0.035mm) mesh screen. The portion retained was wanhed into a graduated cylinder and allowed to settle for a minimum of 24 hours. The supernatant - was withdrawn until ten ml of concentrate remained. One ml of 'this thoroughly mixed cencentrate was placed in an inverted microscope cell and examined at 100X magnifica-tion. All zooplankters within the cell were identified to the lowest practicable taxon and counted. Total density (individuals / liter), Shannon-Weiner (log base 2) and evenness diversity indices (Pielou 1969), and richness index (Dahlberg and Odum 1970) were calculated based ' upon one sample per month which was collected below the skimmer wall f rom one operating intake bay. Seasonal Distribution The zooplankton community of a river system is typically composed of protozoans and rotifers (Hynes 1970, Winner 1975) . The zooplankton com-munity:of:the Ohio-River near BVPS during preoperational and operational monitoring years was composed primarily of protozoans and rotif ers. Total organism . density and species composition of .;ooplankton f rom the Ohio River and entrainment samples were similar during 1976, 1977, 1978, and 1979 (DLC 1980) . Samples collected from intake bays were usually representative ' of the zooplankton populations of the - Ohio River near BVPS. During 1991, ; protozoans - and rot'i f er s accot..n.ed for 98% or more of all zooplankton on all sample dates (Table V-D-1). Total organism densities during the . winter and early spring (January through March) were less than 1,600/11ter (Figures V-D-1, Table V-D-1). Total organism densities increased in April and peaked in May (ll,920/ liter ) . A secondary peak occurred in September when 10,760 organisms / liter were observed; there-54
TABLE V-D-1 MONTHLY ZOOPIANKTO4 GROUP DENSITIES '(Nurnber/ liter) AND PERCENT COMPOSITION FROM ENTRAINMENT SAMPLES, 1991 BVPS Jan Feb: Mar Apr May June _ Group f/L 1 i/L- % i/L- 1 I/L 9 f/L 1 3/L 1-Protozoa 54 0 95 1, 50 0 96 570 85 1,980 99 .10,840 '91 2,640 63 Rotifera 30 5 70 -4 100 15~ .30 1 .1,040 9 1,560 37. Crus tacea 0 0 0 0 0 0 0 0 40 <1 0. O
!! 8 Total 570 100 1570 100 670 100 2,010 100 11,920 100 4,200 100 $@
$ 0' nM
-Jul Aug Sep Oct Nov Dec - M e.
Grcup i /L 1 i/L 1 I/L % f/L % f/L % 8/L % y5' m Protozoa 9,920 86 6,240 76 10,080 3,940 ON 94 91 4,720 96 1, 3 50 96 gn 4O Rotifera 1,680 14 1,880 23 '480 4 380 9 160 3 50 4. Eg x 4. Crus tacea 0 0 80 1 200 2 20 <1 40 1 0 0- y o Total 11,600 100 8,200 100 10,760 100 ,4,340 100 4,920. 100 1,400 100' E
. .a ._. _- . . . . . . . _ _ - -.. , , ,
l L CELLS'/ LITER 100000' ___-_ _ _ __ _____ _ __-_;= ;-.__ _ _______
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f I i 1 1 I f I f I f I O JAN FEB MAR APR MAY- ' JUN JUL AUG SEP OCT NOV:DEC -
-MONTH E
O PREOPERATION'AL YRS. ! - MERAGE 1976-1990 0 1991 - FIGURE V-D-1 I MONTIILY ZOOPLANKTON DENSITIES IN THE 01110 RIVER DURING PREOPERATIONAL (1974-1975) AND OPERATIONAL (1976-1991) YEARS
.. BVPS p -w . S *
. - - .__ . _ ~.
DUQUESNE LIGHT COMPANY 1991 ANNUAL ENVZRONMENTAL REPORT af ter densities decreased gradually through December. The maximum zoo-plankton density ~ in the Ohio River near BVPS frequently occurs in the spring, although it is - sometimes delayed until summer or early fall (Table V-D-2, Figure V-D-1). Low precipitation and warm weather during the late spring and summer of 1991 provided optimum conditions for zooplankton populations to develop in 1991. The effect of a dry year and low river discharges was noted by Hynes (1970) to favor plankton populations. The seasonal pattern of zooplankton densities observed in the Ohio River near BVPS is typical of those in temperate climates (Hutchinson 1967) . Zoopienkton densities in winter are low due primarily to low water temp-erature and limited food availability (Winner 1975). In the spring, food availability and water temperatures increase, which stimulate growth and reproduction. Zooplankton populations decrease during the fall and winter f rom the spring or summer maximum becauce optimum condi-tions for growth and reproduction decrease during colder months. Densities of protozoans during January through March of 1991 were between 540 and 1,500/ liter (Table V-D-1). Protozoans peaked in May and September. Thereaf ter, populations progressively decreased in December ! to _ densities of 1,350/11ter. Vortice11a sp., Strombidium sp., and Tintinnidium = fluvitale were the common protozoans throughout the year . Vortice11a sp. or Strombidium sp. dominated the protozoan assemblage during nine months (Table V-D-3) . The most abundan t protozoan in the other months was Tintinnidium (Jona, August, and September) . These taxa have been a main part of the protozoan assemblage of the Ohio River near BVPS since environmental studies were initiated in 1972 by Duqut:sne Light Company. .
-The rotifer assemblage in 1991 (Figure V-D-2) displayed a typical pattern of rotifer popula tions in tesaperate inland waters (Hutchinson :
1967). Rotifer densities increased from a minimum of 30/11ter in January to a maximum of 1,880/ liter in August; a small secondary peak did not occur in 1991 (Table V-D-2). Rotifer populations generally
- j. decreased = af ter August to densities of 50/ liter in December. Rotifers t-l l-l 57 l
. TABLE V'D-2
- MEAN ZOOPLANKTON DENSITIES (Number / liter): BY MONTH .FROM 1973 THROUGH 1991, OHIO RIVER 'AND DVPS Total' fooplankton : Jan Feb Mar- Apr May ' .7un Jul Aug Sep Oct Mrsw ' . Dec 1973 (a) 50 90 154 588 945 '1,341 - -
425 180 87 1974 78 56 96 118- 299 625 4,487 .3,740 1,120 1,321 :-- - 1975 .
~
4.426 3,621 1.591 2,491 6234 1976 327 311 347 .10,948- 2, 51 6 5,711 3,344 3,296 . 3, 521 ' 518 446 577
'1977 147 396 '264 393 5,1 53 4,128 1,143 1, 503 3,601 553 934 486-1978 31 30 20 35 403 1,861 1, 52 6 800 1,001 '435 297' 60 1979 357 96 228 - 53 4 2,226 599 2,672 4,238 950 370 542 550 1980 320 -265 389 ' 270" 53 0 420 3,110 490 2,020 3,820 '1,030. 70 0 1981 190 360 220 580- 840 310 3,800 1,940 4,490 1,8 50 760 370 "'
1982 400 320 340 880 ' 4,650 1983 285 330 1,415 540. 480 1,020. 8,220 5.630 4,780 5,170 6,010 5,520 3,280 6,410 2,880 2,300 1,030 3-9 50 560 1984 270 290 295 290 560 1, 52 0 610 1,380 6,700 -6,080 570 390 do. 1985 410- 485 6, 520
- 1986 3 50 3 50 255 360-365 860 14,280 6,280 1,650 1.,920 6,390 10,000 11,040 4,680 14,760 4,760 1,815 740 590 570 3 50 cc 1987 550 1,330 ' 1,8 50 600 36,000 14,080 11,550 7,800 3,920 1,400 4, 680 1988 1,120 400 370 2, 52 0 4,440 18,420 15,080 8,160 6,320 6,020- 2,160 900 $ E- 2 770 1989 710 855 825 885 735 1990 825 539 900 800 2.325' 2,340 1,21 5 3,330 1,800 5,420 2,0 54 1,995 960 470 E "1 990 19,280 1,716 1,183 512 1991 170 .1,570 670 2,010 11,920 4,200 11,600 8,200 10,760 4,340
$[.
w 4,920 1,400 :o a Protozoa Q= 1973 - 45 - 63 82 186 56 331 346 135 29 H g-58 1974 50 42 72 91 138 409 1,690 716 1,006 4,195 - -
$p 1975 - - - - - - -
S35 3,295 1,141 2,239 4 52 20 - 1976 278- '274 305 10,774 1,698 6 1,903 1,676 808 425 396 492 $ 1977 135 365 236 4, 50 9 1978 18 14 14 312 27 332 2,048 1,360 808 407 947 315 2, 529 256 401 222 825 227 344 26
.]
as - 1979 312 64 188 3 80 2,052 459 340 712 609 326 '4 54 328 d 1980 244 ~ 25C 3 54 190 390 370 1,620 380 1,180 3.010 .760 640 1981 130 310 '180 510 480 - 230 730 1, 2 50 4,020 1, 580 550 330-1962 3 50 310 310 820 1,300 870 2,360 1,560 1,590 4, 8 50 2.060 980 1983 2 50 320 115 500 390 6,940 1,320 5.030 1,100 1,670 890 490 1984 225 280 285 260 50 0 1,190 530 1,210 5,000 5.300 53 0 3 60 1985 J65 455 230 355 3,280 4.440 1.340 6,680 1,860 4,080 670 52 0 1986 330 330 300 760 11,220 1,290 5,970 7, 520 9,780 1,680 490 305 1987 500 1,260 1,725 480 36,000 9,360 10,080 6,7 50 3, 520 1,030 4,320 72 5 1988 1,080 345 330 2,360 4,020 8,580 10,720 7,000 5,000 5,720 2,040 T10 1989 680 795 780 780 70 5 2,200 2,910 400 3,000 1,575 900 430 1990 7 50 525 800 710 2,085 1,140 960 15,520 1,911 1.560 1,118 432 1991 54 0 1, 500 570 1,980 10,840 2,640 9,920 6,240 10,080 3,940 4,720 1, 3 50
TABLE V-D-2 (Continued) May Jun Jul Aug. Sep Oct Nov Dec Rotifera Jan Feb _ Man .Apr 859 1,001 - .75 43 27 5 - 25 64 388 1973 - 2,783 2,939 115 120 - - 26 12 22 24 155 213 1974 - - - .- 3,339 313 444 2 50 164 1975 1,398 1,597 2,643 89 48 78 48 36 38 169 808 4,864 1976 1,984 .328 539 1,022 147 108 136 12 31 26 76 631 1977 24 72 61 67 47 22 48 29 33 15 14 16 1978 2,255 3,482 324 42 86 220 44 3? 37 151 172 135 1979 1,470 110 790 780 260 50 72 it 33 80 140 50 1980 80- 2,800 630 470 260 210 40 y
.40 50 40 70 340 to 1981 3, 2 50 1, 550 3,840 1, 52 0 240 40 3,340 130 1982 50 10 10-30 1,100 50 40 90 1,270 3,440 880 1,930 1,190 60 70 $
1983 30 1,700 780 40 3e 330 80 160 1984 45 40 10 30 10 25 30 10 40 3,240 1,820 580 2,880 2,740 660 70 40 $8 1985 1986 20 20 60 100 3,060 300 330 3,280 4,560 120 370 100 320 45 175 2m 120 0 4,720 1,400 950 280 1987 40 70 125 120 60 C' $ - 420 9 , 54 0 4,240 1,000 1,320 260 1988 40 45 40 1 60 30 140 420 920 2,360 390 60 40 m5 90 1949 30
~60 60 14 45 90 80 225 75 30 3,680 143 1 56 65 72 Me 1990 1,680 1,880 480 380 160 50 1991 30 70 100 30 1,040 1,560 M9 in U -* Crustacea t1 0 9 - 3 2 2 1973 - 1 - 1 3 6
12 3 2) 85 7 6 - - %. @-o 3 2 3 3 1974 2 gt-51 12 6 3 6 C' $ g< 1975 23 69 3 2 8 2 1 5 4 10 141 '(I 197E 13 96 7 17 50 5 1 6 m
- - 2 5 O 1977 48 12 27 75 9 5 5 i 6
1978 4 6 3 2 3 2 4 78 44 17 2 2 2 4 1979 1 0 3 30 10 10 0 0 20 0 50 3 1 1 0 1980 2 70 60 0 10 0 0 l 20 0 0 0 20 0 l 1981 20 60 90 to 0 10 0 0 0 10 10 20 1982 20 100 2 50 20 0 0 5 0 0 0 0 10 1983 0 0 0 0 0 0 20 0 0 10 1984 0 0 le 0 20 0 440 *3 20 0 5 0 0 0 0 1985 90 240 (20 15 0 0 0 0 0 60 1996 0 0 0 0 0 0 70 100 120 10 0 0 0 1987 80 160 0 40 0 0 10 0 0 0 300 1988 0 60 30 0 0 0 15 0 0 0 480 1989 0 0 0 0 8 0 80 0 15 0 10 10 15 0 1990 0 30 200 20 40 0 0 0 0 0 40 0 1991 I*I ) Mo sams.le collected.
- ar TABLE V-D-3_.
DENSITIES (Number / liter) ' OF 'MOST ABUNDANT ZOOPLANKTON TAXA (Groster thin 2% on any dato)' - COLLECTED FROM ENTPAINMCIT SAMPLES - JANUARY THROUGH DECEMBER, 1991 BVPS Tama Jan Feb Mar' h 'May . Jun ' Jul g 'Sen Oct ' Now Dec PR&r020A ' Arcella sp. 50 10 - 20 30 20 20
- Codmella cratera 10 10 20 100 40 80 80 .20 Cyphoderla ampulla 20 20' 20 10 Didinium sp. 200 40 -Difflugia sp. 201 10 - 10 40 40 40 Dileptus bivaeulatus 40 320 200- : 20 -- e Epistylis' -
60 '* Rolophyric .lliate s 220 280 40 40 160' 40 20 40 Nuclearia slaplex 10 1,200 320 520 20 20 20 Opercularia sp. 20 30 $ 8.- Or. O ; Paradileptus sp. 640' Parameetum sp. 10 50 40 80 40 5$ Staurophrya elegans t' $ 240 80 Strombidium ep. 50 10 en @ 200 Strobilidium gyrans 10 10 40 1,760 80 5,080 80 960 240 2,320 720 . 1,880 660 2,720 150 .kw p 300 50 *4 Tintinnidium fluvitale 380 680 1,320 1,480 2,520 6,280 300 160 30 59 Tintinnopsi_s cylindrica trachelius sp. 20 40 40 '640 10 bO Uronema sp. 20 50 to %g Urotricha sp. 10 110 160 120 100 100 gg. m, o Vortice11a sp. 290 .1,090 400 4L 3,440 Ciliate unidentified 20 40 20 10 160 440 40 680 80 1,360 200 280 660 680 990 FD 80 20 10 .. g k ROFIFERA O Collotheca sp. 160 80 k Conochilus unicornis 40 40 40 120 240 100 20 Benarthra mira 120 Keratella cochlearls 10 20 10 440 240 360 40 80 140 80 Polytrthra dolichopters 10 80 640 880 560 40 140 60 10 i Polyarthra vulgaris 280 40 Synchaeta sp. 10 10 10 320 120 560 Trichocerca pusilla 80 320 Rotifer unidentified 20 120 40 200 40 10 Total 200PIANK7CN $70 1,570 670 2,010 11,920 4,200 11,600 8,200 10,760 4,340 4,920 1,400 ' Total of Most Abundant Taxa 540 1,370 160 1,470 9,040 4,000 11.280 7,880 10,240 4,220 4,820 1,340 Percentage Composition of Most Abunde.nt Zooplankton 95 87 84 73 76 95 97 96 95 97 98 96 i
v sg. NUMBER / LITER
-12000 ~10000 - ---
I
/
8000= -
\
6000 \ EE 5e
/ :: g -
=
e 4000= -
/ a g 2a.
~
\ 85'
\ @n
^ s 5s 2000 - -
~
ji
^ -
0 1 1 1 1 e i i i 6 i 1 4 JAN FEB MAR APR MAY JUN , JUL AUG SEP OCT NOV DEC MONTH
~ CRUSTACEA 0 ROTIFERA C PROTOZOA FIGURE V-D-2
' ZOOPLANKTON GROUP DENSI*f1ES
'FOR ENTRAINMENT SAMPLES; 1991
-BVPS
_ - _ . . _ = Dd9UESNS LIGliT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT were. the second 'most abundant group during 1991. Keratella cochlearis and Polyarthra dolichoptera were the most abundant rotif ers during most _ off the year ~ (Table V-D-3) . CrustaceanJdensities were low (0 to 200/11ter) throughout 1991 (Table i V-D-1) . Most crustaceans were collected during summer; the peak density ' of 200/ liter occurred in September (Figure V-D-2) . Crustacean densities never exceeded protozoan or rotifer densities and constituted f rom 0 to 2% of the total zooplankton density each month (Table V-D-1) . Copepod nauplii were the most ~ numerous crus tacea n's collected during 1991. Despite the low precipitation in 1991, crustacean populations did not j develop high densities due to unfavorable flow and turbidity conditions ! in the river during 1991. Crustaceans are rarely numerous in the open I i waters of rivers and many are eliminated by silt and turbulent water 1
- (Hynes 1970) .
The highest Sha'nnon-Weiner diversity value of 3. 42 occurred in August while the maximum number of species (26) occurred in July (Table V-D-4 ) . Evenness ranged f rom 0.44 in December to 0.78 in June. Richness varied f rom a low of 1.5311n November to a high of 3.02 in April. The number of species ranged from 14 in November to 26 in July. Low diversity indices during December reflect the dominance of Vorticella. Comparison of Control and Non-Control Transects Zooplankton samples were not collected from stations on the Ohio River after April 1, 1980;- theref ore, comparison of Control and Non-Control transects was not possible. Comparison of Preoperational and Operational Data - Popula tion dynamics of .the zooplankton community during the seasons of pr eoperational and operational years are displayed in Figure V-D-1. Total zooplankton densities were lowest in winter, usually greatest in summer, and transitional in spring and autumn. This pattern in the Ohio -River sanetimes varies from year to year which is normal for zooplankton 62
TAE.*C V-D-4
' ZOOPLANKTON ' DIVERSITY INDICES BY MONTH FOR ENTRAINMENT SAMPLES,.1991 LBVPS'
- l. .
Jan Feb Mar ' - Apr May Jun No. of" Species - 15 20 ;20 24 22 19: Shannon-Weiner Index 2.73- 2.05' 2.64 3.19 3.17 3.32 0.70 0.47 0.61 0.70 0.71 0.78' Evenness 40 2.24 - f, i 2.21 .2.58- .2.92 3.02 2.16 Richness
>m Jul Aug Sep Oct Nov Dec'. x ta p ;.
mm No. of Species 26 24 20 19 14 19 20' hC-
- 5o
' g *i W Shannon-Weiner Index 2.97 3.42 2.07 2.75 2.21 1.86 2.70 e 8-Evenness 0.63 0.75 0.48 0.65 0.58 0.44 0.63 g4 c g-Richness- 2.67 2.55 2.05 2.15 1.53 2.49 2.38 g*
8 5
. . . . . . . . . . . . . . . . , . , . . ~ . . . . . . . . . . . . . . , . . . . . . . , . . . . . . ,,, . . . . ......,-......._...,.._...........-,_..._......................._.......__.,,..._.....,__..,__...
DUQUESNE LIGHT COMPANY 1991 ANNUAL ~ ENVIRONMENTAL REPORT populations in other ' river habitats. Hynes (1970) concluded that the
-zooplankton community of rivers is inherently unstable and subject to L constant change due to variations of temperature, flow, current, turbid-ity, ' and - f ood source. Total densities of zooplankton during 11 months of -19911 exceeded the average range established during the preoperational years (1973 through 1975) 'and operational years (1976 through 1990) .
(Figure --V-D-1) . In 1991, the data indicate that the peak zooplankton densities occurred in May and September.
. The species composition of zooplanir on' in the Ohio River near BVPS has remained stable during preoperational and operational years. The common or abundant- protozoans since 1972 have been Vortice11a, Codonella, Difflugia, Strobilidium, Cyclotrichium, Arcella, and Centropyxis. The most numerous _ and frequently occurring rotifers have been Keratella, Polyarthra, Synchaeta, Branchionus, and Trichocerca. Copepod ' nauplii
'have been the only crustacean taxon found consistently. Community structure, as compared by diversity indices, has been similar since 1972 (Table V-D-5) . In previous years, low diversity indices and number of - species occurred in winter; high diversities and number of species usually eccurred in late cpring and summer. The low diversi ty indices in December 1991 reflect the ' high numbers of the protozoan Vorticella. In 1991, the diversity indices and species numbers were moderately low lIn January and February which was typical for months of winter and early spring.- Shannon-Wiener diversity indices in 1991 ranged from 1.86 to' 3.42 and were similar to the range 1.80 to 3.28 that occurred during preoperational years from 1973 to 1975. The variation in evenness during 1991 (0.44 to 0.78) was usually at the upper portion of the range reported from 1973 to 1990 (0.21 to 0.93). Summary and Conclusions Zooplankton densities throughout 1991 were typical of the temperate zoo-plankton community found in large river habitats. Total densities 64
g . TABLE V-D-5'
. MEAN ZOOPLANKTON DIVERSITY INDICES BY', MONTH FROM -1973 THROUGH 1991 IN THE OHIO RIVER NEAR BVPS-Jan Feb Mar Apr May 'Jun Jul Aug _Sep Oct Nov Dec 1973 .
(a) Number r>f Spe les 8.44 15.29 '21.28 25.07 21.96 22.86 16.33 '14.40 14.30. Shannon Index M 1.80 3.06 3.08 2.79 2.25 2.20' 2.21 2.31 '3.10 Evenness '0.37 0.63 0.58 0.46 0.39 0.36 0.37 0.44 0.61 1974 9.18 17.75 23.25 15.56 21.14 9.55 14.47 Number of Species 14.64 '14.92- 18.89' ~ 3.18 2.53 2.91 3.06 3.25 2.32 '3.28 '2.24 '.2.15 1.84
- Shannon Index
- Evenness 0.62 0.56 0.57 0.58 0.55 0.41 0.60 0.41 0.42 0.30 w.
1975 .
$ E' Number of Species 24.75 3.20
'18.75 1.86 14.39 2.90 17.44 2.01 15.38 3.20
>M' Shannon Index Evennets ; 0.69 0.44 0.77 0.49 0.82 $
1976 9 ".:
- <g 23.56 11.19 " *
- Number of Species 7.00 9.13 8.69 17.56 19.19 23.56 28.06 23.50 8.75 11.75
'h Shannon Inder Evenness-1.67 0.60
-2.64 0.84 2.24 0.73 0.89 0.21 3.06 0.72 2.33 0.51 3.36 0.70 3.63 0.80 2.76 0.61 2.73 0.79 1.60 0:51 2.64 0.75 hh gd gO g@.
1977
- Number of Species 4.30 .10.00 12.00 13.31 21.00 25.62 22.88 25.50 36.75 16.88 13.31 15.31 > *3 Shannon Index 1.53 2.59 3.01 2.98 3.15 3.45 3.32 3.60 3.71 0.71 3.35 3.42 3.42' "$
Evenness 0.78 0.79 0.87 0.81. 0.72 0.74 - 0.73 0.77 0.82 0.79 0.86 M *< M "J 1978 O Number of Species 0.12 7.12 4.31 5.12 7.62 6.25 10.25 11.25 12.50 0.25 10.8r 10.38 s Shannon Inden 2.48 2.41 1.53 1.70 1,53 1.31 2.50* 2.44 2.53 2.28 2.15 2.00 Evenness 0.83 0.85 0.74 'O.71' -0.52 0.50 0.76 0.70 0.70 0.73 0.62 0.83 .I A979 Number of Species 10.62 6.00 10.25 15.88 17.25 14.25 16.88 21.50 18.12 12.00 14.62 14.00 Shannon Index 2.51 2.52 3.05 3.42 .2.36 3.02 2.42 3.30 3.36 2.99 2.84 3.10 Evenness- 0.74 0.93 0.90 'O.86 0.58 0.80 0.60 9.74 0.80 0.84 0.74 D.83
+
0c$mmgt o **r*bq o$*3E
* $ W >=@0' c- ,t ok
- h,E.m$>I $$9 -'
060 074 047 04 5 022 073 00 0 ce 03 0 04 058 . 057 095 01 D
- 7. _ 0 1 7. . 7 1
83 0 1 020 730 . 830 120 310 1 s0 1 1 1 ' - 1 2 068 065 043 080 094 056 032 v 027 066 058 . 02 087 027 087 o 8. . N 830 1' 720 1 930 1 73 0 1 420 1 -
.1 930 520 1
084 059 091 03 8- 04 7 076 00 t c 086 006 006 04
- 6. -
086 027 097 . O 220 130 4 10 31 0 920 030 7I0 2 2 ' 3 3 1 2 1 037 020 062 025 020 028 094 p 027 e 066 0 8 7., 0 9 7.. 0 6 8.. 077 01 8 S 830 020 030 730 330 730 24 0 1 2 4 3 2 2 3 091 057 083 054 084 002 098 g 077 057 028 065 025 067 06 7 u . A 520 430 640 020 820 23 0 630 1 2 3 3 1 3 2 032 065 023 060. 007 050 l 068 096 0 87 057 046 03 8 04 096 5 . u J 130 320 730 4 30 220 830 32U
?~ 2 3 1 1 1 2 5) n 01 4 036 0' 04 061 033 a18 04 4 097 077 027 035 066 078 d u 520
- n. 9 6 De J 1
220 1 2 030 4 20 2 820 1 1 920 230 E u ' 2 Vni
'E t Ln y 00 0 041 062 04 6 061 002 06 4 B o a 006 048 04 5 058 026 097 027 AC M 820 9 3.0 720 . 730 320 620 120 T( 1 2 1 1 1 2 012 027 090 0 91 003 04 9 054 r 047 036 058 008 . 016 064 p 017
'A 020 120 230 4 30 010 1 1 2 1 020-1 1 930 1
034 081 093 013 028 .023 030 r 508 028 088 045 082 075 018 a M 230 720 120 320 . 700 910 530 1 1 ' 2 1 008 024 020 091 04 9 085 04 6 b e 077 008 027 . 0 3 7.. 067 095 087 F 120 230 920 020 020 210 320 1 1 . 1 1 1 1 210 041 090 006 . 090 022 073 n 657 017 099 027 028 036 098 a J 12O 82O 020 830 . 730 320 220 1 1 1 1 1 1 s s s s s s s
- e. ^ i e
i e i e' i e i e i e' e c c c c c c ex' pe ex pe er pe ex pe ex pe ex ex pe pe Sd Sd Sd Sd Sd Sd Sd n n' n n n n n f i fi fI . fi fi fi f I o s o s o s o s o s o s o s ns ns ns ns ns ns n: roe . roe r oe r oe roe roe roe enn enn enn enn enn enn enn 0 bnn 1 bnn 2 b nn 3 b nn bnn 5 Dnn b nn 8 9 mae uh v 8 9 mae uhv 8 mae 8 mae 4 8 mae 8 mae 6 8 ma e 9 uhv 9 uhv 9 uh v 9 uh v 9 uh v 1 NSE 1 NSE 1 N SE 1 HSE 1 NSE 1 NSE 1 NSE em. s a
i I TABLE V-D-5 (Continued) Jun Jul_ Aug Sep Oct Nov Dec Jan Feb Mar Apr .. A 1987 28.00 25.00 20.00 20.00 16.00~ 16.00 Number of Species 13.00 14.00 16.00 14.00 9.00 20.00 0.89 3.15 3.53 3.50 3.25 3.37 2.32. 3.48 Shannon Index 2.64 1.76 3.40 3.54 0.5; 0.73 0.73 0.75 0.76 0.78 0.87 Evenness 0.71 0.46 0.85 0.93 0.28 e.* e 1988
- 13.00 24.00 14.00 24.00 .2&.00 22.00 16.00 21.00 ,.
Number of Species 8.00 17.00 17.00 13.00 2.35 2.97 2.68 2.30 2.60 3.?O 2.29 '3.20 3.48 Shannon Inden Evenness 2.45 0.82 2.57 0.62 2.70 0.65 0.62 e.70 0.72 0.60 0.70 0.74 0.53 0.74 0.61 $8 2O 1909 5$ em 11.00 15.00 15.00 12.00 18.00 18.00 21.00 22.00 14.00 14.00 13.00 E Pumber of Species 14.00 3.35 3.20 3.49 2.82 3.21 3.43 3.46 Shannon Index 2.37 2.68 3.02 0.77 3.22 0.82 2.91 0.81 0.77 0.82 0.79 0.75 0.84 0.92 0.72 NC Evenness 0.62 0.77 29 m kQ 4 1990 Rn 2o 18.00 12.00 11.00 21.00 19.00 17.00 12.00 13.00 Number of Species Shannon Inden 16.00 3.02 13.00 2.46 19.C3 3.53 16.00 2.95 2.73 2.52 2.54 3.07 3.07 3.35 2.87 2.40 $4 C 2* 0.66 0.70 0.73 0.70 0.72 0.82 0.80 0.65 0.76 0.67 0.83 0.74 Evenness M5 Q 1991 O. Number of Species 15.00 20.00 20.00 2s.00 22.00 19.00 26.00 24.00 20.00 19.00 14.00 19.00 $ 3.32 2.97 3.42 2.07 2.75 2.21 1.86 2.73 2.05 2.64 3.19 3.17 Shannon Index 0.78 0.63 0.75 0.48 0.65 0.5s 0.44 Evenness 0.70 0.47 0.61 0.70 0.71
._ y '
I*IBlanks represent periods when r:0 collections were made. (b)Shannon-Weiner Inden WData for period April 1980 December 1991 represents single entrainment samples collected monthly. l
DUQUESNE LIGHT COMPANY $ 1991 ANNUAL ENVIRONMENTAL REPORT exceededI the range of those reported in preoperational and several operational years. Populations developed highest densities in May and a secondary peak occurred in - September. Protozoans and rotifers were always; predominant. Common and abundant taxa in 1991 were similar to those reported - during preoperational and operational years. Shannon-Weiner diversity, number of species, and evenness were within the ranges of-preceding years. Based on the data collected during the 16 operating _ years-~(1976 through 1991) and the three preoperational years (1973 through 1975), it is concluded that the overall abundance and species composition of the zooplankton in the Ohio River near BVPS has remained stable and possibly improved slightly over the nineteen-year period f rom 1973 to 1991. The data indicate that increased turbidity and current from high water conditions have the strongest ef fects of delaying the populations' peaks and temporarily decreasing total zooplankton densi-ties in the Ohio River near BVpS. E. FISH Objective ' Fish sampling was conducted in order to detect any changes which might
. occur in fish populations in the _ Ohio River near BVPS.
Methods
- Adult fish surveys - were per formed in May, July, September, and November 1991. During each survey, fish were collected at the three study trans-ects ' (Figure V-E-1) using gill nets, electrofishing and minnow traps.
The gill nets consisted of five 25-ft. panels of 1.0, 2.0, 2.5, 3.0, and 3.5 inch iguare mesh. Two nets were positioned at each transect, one angled along _each shoreline, with - the small mesh positioned inshore. At Transect 2 the river is divided by Phillis Island into two separate channels,.the main channel (2A) and the back channel (28). Two gill nets were set in each of these channels, resulting in a total of eight 9111' nets set per sampling date. 68
- .e .. .
%id l
En 2 n.y g, - m
? %.ih wup Nd N iM
+#wyma.
-9 MIDLAND,
** nwa ws 1 s s
.a s ,3
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-N e
- %"i ggre \
--- e 4, nwsrzmo m cE . :;; .
n%g.%,. m:ms ,
- rz.wr -
M #e 4 ga
.* TTM 9%%Asi!+3 .
E8
/' . , . N . "****""L- CC.
> !U
/ t~ tn
\
[> "' 1 z 3 ' O v
, . .8. . R t-.
mO 8 . " ,, ;- 6:~ 84 O\ snoor.s 6a ZO t .: 2 A 4y i* yo LEGFND 1- 3 STATICW Nt!MBER t' > g D1 BEAVER VAILET DIScifARGg
, g I N SHING CII.T. NET m{
t9 D2 DIDOSTRIAL DISCHARGE f 2B e AID To NAVIGATION : BEAVER . MDea0W TRAP 0 2"^= = ssIc= I s E vxt.r.rr , , . ;g powra STATION FIGURE V-E-1 ( FISH SAMPLING STATIONS BVPS _ . _ _ _ _ _ _~
-DUQUESNE-LIGilT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT Electrofishing was conducted with a boat-mounted boom electroshocker.
Direct current of 220 volts at one to two aaperes was generally used. The shoreline areas of each transect were shocked for ten minutes during each survey. Minnow traps were baited with bread, cheese and sucrose then placed next to the inshore side of each gill net on each sampling date. These traps were painted black and brown with a camouflage design and were set for 24 hours before they were removed and checked for fish. Fishes collected using gill- nets, elect.rofishing and minnow traps were
- processed ' according to the following procedures. All game fishes were identified, . counted, measured for total' length (mm), and weighed (g )
individually. For all non-game fish taxa samples comprised of 30 speci-mens or less, the total length (mm) was mea sur ed for each specimen. Large non-game fishes were weighed individually. Smaller non-game fishes (e.g. , shiner sp.) were separated by species and batch weighed. Subsampling was performed when more than 30 specimens were obtained for a non-game taxa according to methodologies stated in the DLC BVPS Environmental Procedures Manual, Chapter 5, Aquatic Ecological Monitor-ing Procedures, . Section 7.1-4. Live fi5h were returned to the river immediately after the processing was completed.- All fish which were unidentifiable or of' questionable identification were placed in plastic sample bottles, preserved with 10% formalin, labeled and returned to the laboratory. Any - fish which was not previously collected 'at BVPS was retained for the voucher collection. Results Fish population surveys have been conducted in the Ohio River near BVPS from 1970 through 1991. These' surveys have collected 66 fish species and three hybrida . (Table V-E-1) . In 1991, 37 fish species,. represented by 3,490 individuals were - collected near ' BVPS - by gill netting, electro-fishing and minnov traps (Table V-E-2) . This total accounted for the highest total catch-per-unit-effort to date for DVPS surveys. This was due primarily to the large number of gizzard shad collected by electro-70
DUQUESNE LIGitT COMPANY j 1991 ANNUAL ' ENVIRONMENTAL REPORT l TABLE V-E-1 l' (SCIENTIFIC AND CO*1 MON NAME)I FAMILIES AND SPECIES OF FISH COLLECTED IN THE NEW CUMBERLAND 1 POOL OF THE 01110 RIVER, 1970-1991 BVPS l Family and Scientific Name Common Name Lepisosteidae (gars) Lepisosteus osseus Longnose gar Clupeidae (herrings) Alosa chrysochloris Skipjack herring . Dorosoma cepedianum Gizzard shad ' Hiodontidde-(mooneyes) Hiodon alosoides Goldeye H. tergisus Mooneye , l l Salmonidae (salmon and trouts) Salmo gairdneri Rainbow trout Esocidae (pikes)
-Esox lucius Northern pike E. masquinongy Muskellunge E. lucius X E. masquinongy Tiger muskellunge Cyprinidae - (minnows and carps)
Campostoma anomalum Central stoneroller Carassius auratus Goldfish Ctenopharyngodon idella Grass. carp Cyprinus carpio Common carp C. carpio X C. auratus Carp-goldfish hybrid Ericymba buccata Silverjaw minnow Hybopsis storeriana Silver chub
. Nocomis micropogon River chub
-Notemigonus crysoleucas Golden shiner Notropis atherinoides Emerald shiner N. chrysocephalus' Strip. d shiner N. hudsonius Spottail shiner N_. rubellus Rosyface shiner N,.-spilopterus Spotfin shiner N. stramineus Sand shiner N_. - volucellus Mimic shiner Pimephales notatus Bluntnose minnow P_. promelas Fathead minnow Rhinichthys atratulus Blacknose dace Semotilus atromaculatus Creek chub 1
l l l I
-l 71 1
DUQUESNE LIGHT COMPANY
-1991 ANNUAto ENVIRONMENTAL REPORT u
6 F TABLE V-E-1 (Continued) Family and Scientific'Name Common Name Catostomidae (suckers) Carpiodes carpio River carpsucker C. cyprinus Quillback C_. velifer Highfin carpsucker Catostomus commersoni White sucker Hypentelium nigricans Northern hog sucke . Ictiobus bubalus Smallmouth buf f air, I. niger Black buffalo l Mexostoma anisurum Silver redhorse tb carinatum River redhorse pb duquesnei Black redhorse tblerythrurum, Golden redhorse pb macrolepidotum Shorthead redhorse* Ictaluridae (bullhead and catfishes) Ictalurus catus White catfish
-I. melas Black bullhead I_. natalis- Yellow bullhead I. ng ulosus Brown bullhead I. punctatus Channel catfish Noturus flavus Stonecat Pylodictis olivaris' Flathead catfish Percopsidae (trout-perches)
Percopsis omiscomayeus Trout-perch lCyprinodontidae (killifishes) Fundulus diaphanus Banded killiftsh 2 Atherinidae (silversides)
'Labideathes sicculus Brook silverside i Percio.thyidae (temperate basses)
Motor chrysops White bass
!b ch'rysops x gb saxatilis Striped bass hybrid ;
Centrarchidae (sunfishes) Ambloplites rupestris Rock bass Lepomis cyanellus Green sunfish Jk. gibbosus Pumpkinseed jk, macrochirus Bluegill L. microlophus Redear sunfish
- L. gibbosus x L. microlophus Pumpkinseed-redear sunfish. hybrid Micropterus dolomieui Smallmouth bass M. punctulatus Spotted bass ib salmoldes _ Largemouth bass Pomoxis annularia White crappie P,. nigromaculatus Black crappie 72
i DUQUESNE L1G!lT COMPANY I 1991 ANNUAL ENVIRONMENTAL REPORT TABLE V-E-1 (Continued) a Family and Scientific Name Common Nan.e Percidae (perches) Etheostoma blennioides Greenside darter E. nigrum_ achnny darter E.-sonale Bandeu darter Perca flavescens Yellow perch ' P,ercina caproden Logperch
,P,. copelandi Channel datter Stirostedion canadense Sauget S. vitreum vitreum Walleye Scimenidae (drums)
Aylodinetus grunniens Freshwates drum I et al. (1980). 2 Homenclature follove kobins, EtU (Gilbert, A former subspecies if N_. cor 1964) and previot. sly reported as common shlner, a 4
-1 I 3 h '
73.
6 s NUMBC2 OF FISH COLLECTED AT VARIOUS' TRANSECTS CY GILL NET (G), r2CT K) FISHING . (E} AND MINNOW TRAP (M) IN THE NEW CCMBERLAND POOL OF TW. TI;O' RIVER, 1597~ BVPS- 2 1 2A Percent 2B 3 Grand Total Annual Taxa Annual _E 3 3 3 1 3 E. 3 3 $ 1 1 G_ E 3 Total Total Longnose gar' I # 5 5 0.1 Gizzard shad 3 643 9 1022 1 119 9 1017 27 2881 2903 Mooneye 83.2 3 3 3 0.1 Rainbow trout 1 1 1 0.1 Tiger muskellunge 2 1 1 3 1 4 u.1 Central stoneroller 1 1 1 v.1 Goldfish 2 2 2 0.1 Cn=am carp 22 5 14 12 18 2 12 4 66 23 89 2.6
- Silver chub 3 Dnerald shiner 5 6 1 17 2 3 3 0.1 0 28 3 31 0.9 Mimic shiner 1 1 1 0.' yE Shiner sp. 15 River carpsucker 2 1 2 2 20 35 35 1.0 cO Quillback 3 1 2 9 6 1 7 c.2 yQ 15 15 0.e Z Highfin carpsucker 1 1 Northern bog sucker 1 1 2 2 0.1 b
-J rea11 mouth buffalo 1 1 2 2 0.1 IC
- 1 1 2 C.I w9 Silver redhorse River redhorse 5 2 1 1
1 9 9 0.3 34 Golden redhorse 7 3 3 5 2 2 1 1 2 0.1 %o Shorthead rednorse 1 1 1 17 10 27 0.8 jg 1 1 2 0.1 >o Redhorse sp. 2 Channel catfish 11 12 1 1 3 3 0.1 $
.-' 25 5 79 5 85 Flathead catfish 1 1 2 - 4 6 1 2.4 @*
white bass 32 2 6 1 40 3 9 C.3 g Striped bass 40 1.1 :e d hybrid 15 19 3 33 70 70 2.0 Rock bass 1 1 1 1 2 3 0.1 Green sunfish 1 1 1 0.1 Bluetill 1 1 1 1 2 3 0.1 Smallmouth bass 4 2 2 5 2 5 2 8 14 22 0.6 Spotted bass 11 6 14 26 37 57 1.6 Largemouth bass 1 1 1 1 2 2 4 0.1 Bass sp. 1 2 1 4 4 0.1 white crapple 1 1 1 0.1 Black crappie 1 1 1 2 1 3 0.1 Yellow perch 1 1 1 0.1 Logperch 1 2 3 3 0.1 Sauger 11 6 2 6 25 25 0.7 Walleye 1 3 4 4 0.1 Fresnwater drum 3 1 1 1 4 2 6 c.2 Total 137 668 1 86 1076 1 82 133 1 149 1147 9 454 3024 12 3490
DUQUEQNE LIGHT COMPANY 1991 ant 4UAb ENVIROllMENTAb REPORT fishing, in conjunction with the f avorable river conditions (low flow, low turbidity) encountered during the four 1991 fishery survey dates. The s t riped ba ss hybrid (whi te bass x striped bass) not collected in previous BVPS surveys, was collected for the first time in 1991. Various agencies have conducted fishery surveys in the New Cumberland Pool of the Ohio River in recent years resulting in the identification of fish species not collected during DVPS surveys. The Pennsylvania Fish Commission collected a goldeye in 1990 in the New Cumberland Pool. The Ohio River Valley Sanitation Commission collected a redear sunfish and a redear-pumpkinseed sunfish hybrid during their 1991 New Cumberland Pool fish study. These newly collected fish species have been added to Table V-E-1, bringing the total taxa of fish to 73 for the New Cumberland Pool of the Ohio River. A total of 3,024 fishes, representing 22 species were collected during 1991 BVPS surveys by electrofishing (Table V-E-3). Gizzard shad accounted for 93.3% of the total electrofishing catch in 1991. Shiner species represented 2.1% of the catch. The remaining taxa collectively acccanted for less than 3% of the total catch. A rainbow trout, rot commonly. collected in the Ohio River near BVPS, was collected near Transect 3 during the May survey. This fish may have entered the Ohio Ri'fer f rom smaller tributaries which were probably stocked. Most of the fishes sampl ed by electrofishing were collected in November ( 54. 5% ) . The fewest fish were collected la May (3.2%). It should be noted that " observed" fishes are typically included in the electrofishing catch-per-unit-effort. This is sometimes necessary because of the turbidity and swiftness of the water, although these-conditions were minimal in 1991. When these conditions do exist, it is of ten not physically possible for the collectors to net these stunned fishes and they are identified to the genus level and recorded as
" observed."
Gizzard shad were collected in greater numbers -(2,903 - electrofishing and gill nets) in 1991 _ than in any previous BVPS survey year. This 75
NUMBER OF. FISH COLLECTED CY MONTH BY GILL NET (C), ELECTROFlSHING (E) . AMD MINNCW TRAF (M) - IN THE NEW CUMBERLAND POOL OF THE 0010 RIVER,1991 ' j ~ BVPS. - Percent May Jul Sep WW Crand Total Annual Annual Tau 3 3 M 3 E_ 3 3 3 3 3 3 3 3 E M Total Total Longnose gar 1 1 3 5 5 C.1 Gissard shad 26 15 962 5 2 58 2 1635 22 2881 2903 83.2 Mooneye 2 1 3 3 0.1 Rainbow trout 1 1 1 0.1 Tiger muskellunge 3 1 3 1 4 0.1 Catral stoneroller 1 1 1 0.1 Goldfish 2 2 2 C.1 Common carp 29 11 15 10 19 2 3 66 23 89 2.6 Silver chub 3 3 3 0.1 5
?merald shiner Mimic shiner 21 2 5 3 28 3 31 C.9 $
1 1 1 C.1 , Shiner sp. 20 l a, 35 35 1.0 :: c Fiver carpsucker Ctillback 2 1 1 1 2 8 1 6 6 15 1 7 15 c.2 0.4
> t7 Eighfin carpsucker 1 '
1 2 '2 0.1 $ Nordern hog sucker Smallmouth Inf f alo 1 1 2 2 C.1 $" a y 1 1 1 1 2 C.1 <[ cn Silver redhorse 3 1 4 1 9 9 0.3 :e o Fiver redhorse Golden redhorse 1 1 1 1 2 27 C.1 @@ 2 6 5 4 5 5 17 10 C.8 @g Shorthead redhorse wedhorse sp. 2 1 1 1 1 1 3 2 3 C.1 0.1 gg Chaanel catfish 34 1 15 1 19 2 11 2 79 1 5 85 2.8 Cy Flathead catfish 2 3 3 1 6 3 9 C.3 g< White bass 6 34 40 40 1.1 m I Striped bass hybrid 59 11 70 70 2.0 0 Rock bass 1 2 1 2 3 0.1 4 j Green sunfish 1 1 1 C.1 Bluegill 1 1 1 1 2 3 C.1 Smallmouth bacs 4 1 8 6 2 1 8 14 22 0.6 spotted bass 3 6 30 18 57 57 1.6 Largemouth bass 1 2 1 2 2 4 C.1 Bass sp. 2 2 4 4 C.1 White crappie 1 1 1 C.1
< Black crapple 1 1 1 2 1 3 C.1 Yellow perd 1 1 1 C.1 Iogper ch 3 3 3 C.1 Sauger 2 4 19 25 25 C.7 Malleye 1 1 2 4 4 0.1 Frestwater drum 1 2 1 2 4 2 6 C.2 Total 81 99 78 993 3 207 286 4 88 1647 5 4 54 3024 12 3490 i
l DUQUESNE LICllT COMPANY 1991 ANNUAh ENVIRONMENTAL REPORT fo" ;3 species has a high reproductive potential and Ohio River condi-tions were f avorable in the spring / summer of 1991 for prolific spawning and development (low fl ow , warm water temperatures, arid above average phytoplankton and zooplankton populations in the river). During the 1991 BVPS summer surveys, schools of gizzard shed were repeatedly observed near the water surf ace throughout the river. Communications with the U.S. Army Corps of Engineers (Montgomery and New Cumberland Locks and Dams) also confirmed the abundant population of gizzard shad in the river during the summer of 1991. Gizzard shad " die of fs" were reported during the summer of 1991 by personnel at both of the locks and dams as well as by recreational boaters in the tiew Cumberland Pool. These gizzard shad "dia of f s* were investigated and were attributed to natural causes due in par t to their unusual high number throughout the Ohio River Dasin for 1991. The gill net resulta varied by month with the highest catch in iptember (207 fish). T30tay, July and November gill net totals were all similar with catches of 81, 78 and 88 fishes, respectively (Table V-E-4) . Gill net sampling typically results in catching more fish in warmer weather when fish are usually more active. The warmer than normal river water temperature (55-60 !P) and low flow condition during the November survey may account for the higher than usual total for that month. The most common species collected by gill nets in 1991 were channel catfish (17. 4 % ) , striped baas hybrid (15. 4 %) , common carp (14. 5%) , spotted bass (12.6%) and white bass (8.8%). A total of twelve fishes were captured using minnow traps in 1991 (Table V-E-2). Emerald shiners, channel catfish, rock bass and freshwater drum were the species collected in the minnow traps. The most common species (i.e., ' those which contributed more than 24 to
- the annual total catch) collected through the use of gill nets, electro-fishing and minnow traps included the following s gizzard shad (83.2%),
common carp (2.6%) and channel catfish (2.4%). The remaining species each accounted for 21 or less of the total. 77 l
DUQUESNB LICllT COMPAtlY 1991 Allt10AL Eluf!R0llMENTAL REPORT e l l TABLE V-E-4 ) I NUMBER Of PISH COLLECTED 3Y GILL NET, ELECTROFISHING o-AND MINNOW TRAP AT IEANSECTS IN T!!E NLM CUMBERLAND POOL 0F Tlic 01110 RIVER, 1991 BVPS Transect .., C111 Net 1 2A 2B 3~ Total Avera g l May 22 7 24 28 81 20.3 ! July 20 17 13 28 78 19.5 September 71 46 22 68 207 51.8 November 24 16 23 25 88 22.0 Total 137 86 82 149 454 > Average 34.3 21.5 20.5 37.3 . s Electroffshing
- Mwy 38 19 3 38 98 24.5 July 67 492 98 336 993 248.3 September. 22 145 10 109 286 71.5 November- 541 420 22 664 1647 411.8 .
Total 668 1076 133 1147 'J0J4 . Average 167 269 33'.3 286.8 ! Minnow Trap , May 0 0 0. 0 0 0.0 July 0 0 1 2 3 0.8 September 1 0 0 3 -4 1.0 November 0 1 0 4 5 1.3 , Total 1 1 1 9 12 Average 0.3 0.3 'O.3 2.3 78
DU90ESNE LIGHT COMPANY j 1991 ANNUAL ENVIRONMENTAL REPORT i i comparisen of control and Non-Control Transects The electroffshing data complied since 1974 (Table V-E-5) reflects i relatively minor differences in catch-per-unit-effort between the I control Transect (1) and the Non-Control Transects, when examined on a year-by-year basis. The fluctuations in fish catches are more pro- { nounced when making compirisons bttween the years, however. These I i fluctuations are often the result cf natural variables functioning ' within the river ecosystem. Fluctuations in catches occur with changes in the physical and chemical properties of the river's ambient water ) quality. Since electroffshing efficiency depends on the water's conduc-tivity, any sampling conducted during extremes in this parameter will af f ect ca tch-per- uni t-ef f or t. In addition, turbidity and current affect the collectors' ability to observe and catch the stunned fish. Dlrect sunlight also influences where fishes congregate, thus determinir.g their susceptibility to being shocked. Electrof f shing collects mostly small forage wrecies (minnows and shad) and their highly fluctuating annual populations were reflected in differences in catch-per-unit effort f rom year to year and sta.tlon to sta tion. - This was particularly true in 1991 when the profilic popula-tion of gizzard shad in the Ohio River near BVPS produced the highest (;atch-per-unit-effort for electrofishing for the eighteen-year period (1974-1991). Gill nets catch mostly game species and are more indicative of changes an fish abundance. When comparing gill net data for 1974 through 1990
- (Table V-E-6) little change is noted between Control and Non-Control Transects. or between preoperational and operacional years. However, the 1991 gill net catch-per-unit-effort totals were the highest recorded for '
the eighteen-year. period, at-17.3 and 12.9-13,7 for the Control and Non-Control Transects, respectively. These elevated ti als were due to j notably high catches of white bass (Transect 1.1, channel catfish, common i carp, spotted bass and the newly collected taxa in 1991, the striped ! basu hybrid._ l l l 79
TABLE V-E-5 ELECTROFISHING CATCH (FISH / HOUR) MEANS (X) AT TRANSECTS IN THE NEW CUMBERLAND POOL OF . THE OHIO RIVER, 1974-1991 BVPS Tr seet 1 Species' 1974* 1975D 1976 e g,77e ' 3,7,e' g,7,e y,,n o g,,g d 1982d g,,3 d 1984 4 1985' ~19860 1997d 19ee d y, d 1990 6 g,,g d
- longnose ,sr -- - - - - - - - -
1.5 - - - - - - - Clazard shed - 2.1 1.2 -2.0 .- - 3.1 3.0 0.8 69.0 31.5 27.0 36.0 76.5 175.5 93.0 - 964.5 Tiget muskelluage ~- - - - - - 0.8 - - - - - - - - - - Muskellunge - 0.5- - - - - - - - - - - Morthern pike - ' - - - - - - - - - - - - - - - - Pike sp. - ' - - - .
- - - - - 1,5 - . - - g,$ - -
Goldfish- 0.7 2.3 - 0.8 - - - - - - - - - C rp 1.0 12.5 20.8 15.8 5.9 - - - 1.5 30.0'_ 66.0 13.5 9.0 15.0 18.0 7.5 13.5 1.5 Sileer chub - - - - - - - - - - - - - - - - w Cieer chub - - - - - 4.5 y, Golden shiner - - - - - - 0.8 - - 1.5 - - - - - - - Emerald shiner 42.0 441.7 18.7 57.0 22.9 58.4 51.5 151.5 114.8 279.0 12.0 e6.5 Striped shiner . 1.5 - 6.0
- 58. 5 40.5 9.0 10.5 7.5
$U ZC C
Spottail shiner - - - Spotfin shiner 1.5 3.0 1.5 - - 0.9 - 4.8 7.0 0.5 - - - 3.0 4.5 1.5 - - - - Send shiner 57.6 129.1 52.5 95.9 0.8 93.6 32.3 23.2 19.5 6.0 3.0 t9
- Mis
- ic shiner - -
3.5 7.0 0.5 1.6 6.2 3.0 6.0 - - 4.5 9.0 - - - - gM Bluntnose minnow 19.5 1.5 - - - 1.5 . 33.3 72.3 $3.2 57.8 12.8 89.4 15.4 18.0 21.8 9.0 4.5 1.5 4.5 - 1.5 - - -
< c=
oo Creek chub' O.9 - 0.5 0.5 - - - - - ' '- C Stoneroller 59 Blacknose dace . 1.5 - - 1.5 b4 s'tiner sp. - - 78.0 3.0 528.0 114.0 78.0 21.0 15.0
%n
- C O Rieer carpsucker Nk 1.5 -
1.5 Quillback - - - - - - - - - - 1.5 - - - rg White secker - - - 0.3 - - - - -
- 1. 5 1.5 3.0 e2 Northern bog sucker 0.7 - -
1.0 0.3 - - -- 1.5
- 1. 5 - - -
1.5 3:edhorse sp. - - - - - - - - - - - Q S11eer redborse 4.5 - - o 0.0 1.5 3.0 - 3.0 - Dirck redhorse - - - - 0.8 1.0 - - - - - - - - - - - Colden redhorse - - - - - - 1.5 1.5 -
- 1. 5 - 4.w 1.5 - - -
7.5 1.5 4.5 Shorthesd redhorse - - - - - - - 0.8 0.0 - 1.5 - - 3.0 3.0 - - - Tc110w bullhead - - - - - - - - - - - - - - - - - - Crown bullhead - - - - - - - - - - - - - - - - - - Channel catfish - - - - 0.3 - - 0.8 - - - - - 1.5 - 1.5 1.5 - Flathead catfish - - - - - - - - - - - - - - - -
- 1. 5 -
C.stfish sp. - - - - - - - - - - - - - - - - - - Trout-perci. - - - - - - 1.5 - 0.8 - 1, 5 - - - - - - -
~
Banded killifish - - - - - - - - - - - - - - - - - -
*MAY-JUL bggg, gy C
MAY-SD. NOV O MAY, JUL. SEP AND NOV
'MAY, JULY. SEP AND DEC
-- - }
Q-N TABLE V-E (Continued) Transect 1
# d g,,4d .'1985' 0 19870 0 19490 1990d g,,g d 8 D 4 g,gg d 1982[1983 1906 1998 Species'- 1974 f l975 1976*' 197?C ' ' 1978* ' 4 1979" 1900 trook sileerside ' - '.
-- - - - - - - - - 4.5 3.0 1.5 - -
- .- ' 0.5 white bees -. * -
~~ ~ - -
Rock bees" Senfish (Impamis) - - -
- - -- '~ - - - -
hybrid - - - - - - -
- - - 0.3 0.5 - -- -
1.5 Green sunfish -
- - - - 0.3 0.5 - - - 1. 5 - - - - - - -
Pumpkinseed. S.8 1. 5 - 1.5 1.5 - 3.0 - 1.5 , 3.0' O.5 1.5 Bloogill ,. 6.6 :- 1.5 - -
'- 1.5 - - - - 1.5 1.5 - w 3.0 3.0 6.0 Sunfish sp. -
4.6 3.8 4.5 . 9.0 3.0 1.5 3.0 - smallmouth bees ~ 0.9 - 2.3 3.0 0.3 0.5 3.0 ' 3.0 g g' 2.7 - 2.6 4.6 1. 5 ' - 4.5 9.0 1.5 7.5 4.5 - - Spotted bass. ' O.9 - - 3.0 - - 1.5 - - I.5 zo 1.0 1.0 - 0.8 - 0.8 - - '- CC 1.argenouth bees 1.1 - -.
- - -- - ' - 4.5 3.0 3.0 4.5 18.0 - - 1.5
- > rs Bass sp. -- -- -
'- - - 1.5 - - - - -
- e. tn '
white crappie - - - - - - 1.5
- 1.5 - 1.5 - - - - - -
gy Eleck crapple - - - - -
- - - - - - - - - z
$C
-- - - - 0.5 -
Johnny darter - - - - - - - - - 1.5 -
. Bended detter- - - -- - - -
-- yo gg.
- - - 0.3' C.5 - 0.8 - - 3.0 - - - - -
Yellow perch -
- - - - - 1.5 - 3.0 - - 1.5 co - - - - 0.3 - 0.5 -
1.5 6.0 - 3 to ,peren - - - - 1.5 1.5 1. 5 -
@8 Sauger - - - 3.0 - - - -
walleye - -: 0.5 --
- - - - - 3.0 3.0 1.5 1.5 3.0 ' -
'p g
*3 r*g Freshwater drum - - - - - - - - - - - - -
Unidentified' - :- - - 67.5 673.5 304.5 361.5 162.0 60.0 1 CO2.0 Total 150.8 645.2 139.4 235.9 65.6- 250.6 146.9 225.2 176.0 418 5 241.5 N, g O wr- Jut, a. Noc, .0, CmT- SEF, le0V kY, JUL, SEP. AIID WOV
'mY JULY, SEP AND CCC I
TABLE V-E-5 (Continued) Transect 2A. 28. 3 1976 c g,77 c species 1974 8 197sb g,7,e g,7,c 3,gg d 'g,ggd 1932d g ,g y.3 g,gg d g,g,e 19864 198 9 19sa d 39,94 gyn d g,,g d Iongnose gar - - - - - - - -
- - - - - g.5 -
0.5 - Skipjack herring - -
- - - 1.g -
Cirrard shed 0.9 1.0 1.4 0.7 0.3 2.1 2.5 21.5 19.2 19.5 76.5 33.0 57.5 116.0 315.0 80.0 35.0 1119.0 Rainbow trout - - - - - - - - - - - - - - - - - 0.5 Tiger muskellunge - - - - - - - - - - - - - - 0.5 0.5 - 0.5 Muskellunge - - - - - - 0.3 - - - 0.5 - - - - - 0.5 - porthern pike - - - - 0.3 - - 0.2 - - - - - - - - - - Pika sp. - - - - - - - - - - 1.0 1.0 0.5 - - 0.5 - - Goldfish - - - - - - 0.8 - - - - - - - - - - - - 3.3- 6.6 4.2 3.0 10.0' Carp sileer chud - 0.5 0.7 1.2 1.2 6.0 4.8 20.2 9.5 5.0 6.0 5.5 3.0 1.5 9.0 um tieer chub - - - - - - " 0.5 - - - .- Golden shiner - - - - - - - - 0.2 0.5 - - 0.5 - - 0.5 - - gc 13.1 Emerald shiner Striped shiner 67.7 239.9 33.8 23.9 53.7 37.0 163.5 21.8 493.5 22.5 21.5 36.5 31.0 10.0 7.0 7.0 11.5 Eh cC spottail shiner E M tfin shiner 4.3 2.0 6.1 4.9 0.5 0.5 1.0 0.8 1.0 4.0 1.5 0.$ 2.0 3.5 0.5 0.5 1.0 1.0
$$Z 17.4 81.0 52.6 26.2 13.3 10.2 22.8 26.0 M r2 Sand shiner 45.2 25.8 - - 0.5 1.5 0.5 - - -
- c Mimic shiner - '- 1.8 1.1 0.3 2.2 1.0 3.2 4.8 7.0 - -
1.5 0.5 - - - -
$[
co Cluntoose minnow 6.1 31.2 45.3 44.9 21.4 40.8 10.2 5.2 14.2 38.5 0.5 1.0 0.5 e.5 0.5 - - - wg ra Creek chub Stonereller 0.3 3Q DE Blacknose dace Chiner sp. 0.2 40.0 42.5 566.5 299.5 12.5 174.0 18.0 17.5 Eh
*i JE
>3 River carpsucker '
1.5 - . rg Quillback - - - - - - - - - - - - - - - 0.5 - -
,g a-white sucker -
0.5 - 0.3 0.1 . 0.3 - - - S.5 - - - - - - - - M Perthern hog sucker - - - 0.3 0.3 0.3 0.2 0.8 - - - 0.5 - - - - -- 0.5 3 Smallmouth buf falo - - - - - - - - - - - - - - - - - 0.5 M Redhorse sp. - - - 0.3 - - - - - - 0.5 1.5 0.5 - 0.5 - - 1.5 d sileer redhorse - - - - 0.3 - - 0.2 0.2 - 1.5 - - - - 0.5 - - Rieer redhorse - - - - - - - - - - - - - - - - . 0.5 Black redhorse' - - - 0.3 0.3 - - - - - - 2.0 - - - - - - Golden redhorse - - - - - - 0.8 0.2 1.5 1.5 - 1.0 2.0 0.5 0.5 .' . 0 1.0 3.5 Shorthead redhorse - - - - 0.4 - - 0.2 1.5 0.5 - - - 0.5 - 0.5 0.5 Yellow bullhead 0.4 - 0.2 - 0.2 - - - - - - - - - - - - - Erown bullhead 0.4 . 0.2 - 0.1 - - 0.1 - - - O.5 - - - - - Channel catfish - 1.0 0.2 1.1 0.3 0.7 0.5 1.2 '* 0.5 0.5 - 1.5 1.0 - - - 0.5 Flathead catfish - - - - - - - - - - - - - - - 1.5 Catfish sp. - - - '- - - - - - - 0.5 1.0 - - - - - - Trout- perch - - - - 0.i 0.5 0.2 - 0.2 5.0 - - - - - - - -
"MAY- JCL b
AUG. NW
%Y- SET, NOV O MAY, JCL, SEP AND NOV
'MAY JULY. SEP AND DEC
nh.
- .~,
..: s-7-
TABLE V-E-5' ' L(Continued)', , j , t. 1' ' Transect 24, 25, 3-d 19,7d 'g,,,o:.g,,94 !' Species '-1?74 8 -1975b 1976c :g,77c 3,7,e g,7,e ~19008 -19 eld "1982d' g,,3d 39,4d g ,, ,e 1946 1990 8" 1991 4 .l l t 1- -; -~-
... ' Banded killifish- - - - --
0.1 ~.' - - - - - 0.5 -- - - - - -- 3.0 - ' - { .. Erook sileerside - ' - - .- - - ~- - - - - - ., - . white bees -- -
- -- , 0.1 - -. 0.5 - -' - - - -~ -
15.0 10.5 0.5 -- i acck bees . . 0.1 -0.5 :- "0.5- 0.5 0.5- - [ 0.4 - - - c
~ Sunfish (Lepceis) , !
t' j- - bybrid .-
- .- 0.3 ' - :- - 0.2 - -
.Creen sunfish- -- -- - 1.4 - 0.3 ' 0.5 0.2- ' O.2 0.5 - 1.0 ~ 0.5 0.5 - - -
0.5 5 j, Pimaptinseed ~ - O.5 0.7 - ~ 1.0 ~ 0.5 - -- 0.2 0.2 - '- 1.0 - -- - 0.5 - - g Bluegill . 1.9 0.6 0.2 0.3 - . 1. 4 . 0.2 -- 0.8 0.2 . 1.5 1.0 0. 5 .- 0.5 1.5 1.0 0.5 0.5 1.0 * , j ; Sunfish sp. .- . .- ' - - - - -- -- - - - 0.5 0.5 - - 0.5 - 0.5 -
- smallmouth bass 0.8 - 0.6' 1.0 0.3 0.9 2.8 -6.5 5.8 4.0 5.0 2.0 3.5 4.0 4.5 5.0 6.5 6.0 >g'
' spotted bees 0.4 - -
2.7 - :2.1 1. 5 . 0.5 0.8 2.5 9..$ 1.0 2.5 7.5 5. 5 4.0 0.5 -
! so CC i 'Largemouth bass 1.4-- - 1.1 0.7 0.7 0.3 0.2- 0.8 0.5 2.5- - -
0.5 - - - - 0.5 < i Bass sp. - - - - - - -- - - - 11.0 1. 5 2.5 1.0 1.0 4.0 2.0 1.5 [* E ! White crapple -- .- - - 0.1 :- 0.8 - - - 0.5 - 0.5 - ' - - - - 3g Black crapple' O.5 - 0.3 - -- .0.2 - - - - 1.0 0.5 - - - - - 0.5 .g Johnny darter 1.0 ' *1.0' O.4 - 0.1 0.2 - - - - - - - - - - - -
% C+
, -Bended'derter -- - - -- - - - - - - - - -
0.5 - - .- mg.
.u- Yellow perch -- - ' -- - 0.1 .2 0.2 - - -
- 05 - - - - - - - @q 4 -
Logperch.' - - - 0.3 - 0.7 0.2 0.8' O.8 1.0 0.5 - 1. 0 ' - 1.0 - 0.5 1.0 3 ' j- sauger- - - '-- ' - - - 0.5 0.2 - - - 1.0 0.5 1.5 - c.5 4.5 '- Eo
. Welleye - - - - - - - - - - - - - - - -
0.5 - y {. j' Freshwater drum - -- - - - -- 0.2 - - - - 3.0 - 1.0 0.5 1.0 2.0 - ca > Unidentified - - - - - - - - - - 1.0 - - - - - - -
,y,
~ Total' 106.5 359.2 125.3 122.8 72.5 153.6 91.3 224.0 102.3 614.5 219.5 126.0 692.5 477.5 377.5 299.J 87.5 1.178.0 en
-s O
i .. g i *MAY- JUL t bADC, W C MkY- SEP, NOF 2-O pWLY, JUL, SEP AND MOF
'MAY, JULY, SEP AND DEC i
=
s. I i 1 x 1 f-i-
! I
- i. ' .
.i
" - ,%m.q, -,.*J %V-- -+ y.
"w-i .4p i- >- i i-- d+w 11e w a w is. e__
ew.w _ . _ _ _ , _ _ _ _ _ _ _
TABLE [Y-E6 - t GILL' NET CATCH : (FISH /24 - HOUR) L MEANS ' (X) AT TRANSECTSmIN THE NDi C128BERIAND FOOL ' THE OHIO RIVER,' 1974-1991 B' M - ' ' Transect 1 species. 19748 -1975b,19760 19770 '1979 day,7,d 1980' 1991' 1982' '1983' 1984' 19es f 1996' gef 1984* 1980' 19,0* 1991' l 4
~
-Longnose gar -- -
0.2- ~- - - - - . - - - - - -' - 0.3 - -
-~
~
Gingard shed' '. - -- -u - 0.1 - .4 0.1 - 0.1 -1 0.1 0.1 - -- 0.4 Mooneye . - - - - -- - - ,. - - - - - - - -- - -.
- ;Aminbow' trout'. - -- - - - - -- - -- - -- -
0.1 - -- ' , - . - - t Northern pikes - - - 0.1 - - - - - - - - - - - - - - -- ! . Muskellunge _ _ - -- - - - - - - - - - - - - - - . _ -. , t -- C1 9er muskellunge 0.Is 0.1 ' -- - - - 0.1 - col - - 0.3 0.1 .- 0.3 l Goldflah - - - - -- . - - - - - - - - - - - - Graas carp e 1 -'. - - - - - - -- - - - - - 0.1 - - -. e ? 1.2 0.1 ~ ! . Carp 0.8 0.1 0.4 - 0. 6 - - 0. 4 -
.0.9. 'O.2 0.3 0.4 0.4 2.4 1.0 0.8 2.3 I
i Coldfish a Carp hybrid. '- - - - - - - - - - - - - - - - - - gg; gg! ! River carpeucker - -- - - - - - -- - , 0.1 - - 0.1 - - - - CC l ?- Quillback. Righfin carpeucker 0.* 0.2 0.1 0.1 0[3 04
'g,1
$$7 Z white socker
- 03 -
0.2 0.2 - .- - - - - - - - - - - -
- r. " '
Black redhorse ' - - 0.1 - - - X ! f.*.
. j l: cm S ilse r - redhorse - - - - -
0.1 - 0.1 - - - - - - - 0.3 9.6 - :n o '
-t Go1Loen redhorse - - - - -- - - - - - -
0.1 0.1 0.1 0.3 0.3 0.1 0.3 @N' Shorthead redhorse - - - - - - - - - - c.1 - - - 0.3 . - g.1 E , L Redhorse sp.: ' - - - - - , - - - - - - - - - - - - ,I3 ie Black , bullhead
- ' - - - - - - - - - - - - - - - - - *i
- >J Brown bu11 heed 0. 4 ' .- - -
0.1 - - ' - - - - - - - - - - - c- y ; Yellow bullhead - '- - - - - -. - - - - - - - - - -
,Z #
white catfish - '- - - - - - - - - . - - - - - - - re l 4 Channel catfish - .- 0. 8 . - 0.7 0.7 0.2 0.2 0.2 0.4 0.2 - 0.4 0.6 0.4 0.4 0.1 0.5 1.s o
- riathead catfirh - -- - - - - - - - - - - -
0.1 - - - 0.1 Z .! ,,. white bass- - - - - - - . - - - - - 0.2 - - 0.5 0.1 - 4.0 i Striped bass hybrid -
- - -- - - - - - - - - - - - - - 1,9
- Rock bass. - 0.3 - 0.2 0.1 0.2 - - - - - -
0.1 - - - - - i j; Green sunfish - - 0.1 - 0.1 - - ' - - - - - - - - -- - - ,
'Pumpkinseed - - - - - - - .- - -
0.1 - - - - - - - l {' Bluegill . - - - - - - - - - - - - - - - - - - ; !i smallmouth bass - - - - 0.1 0.1 - - - - - - - - 0.1 - - 0.5 - Largenouth bass - - 0.2 - - 0.1. - - 0.1 0.1 - - - - - - - - ! Spotted base
' O. 2 0.7 0.1 -
0.1 - - 0.3 1.6 - 1.0 0.4 0.1 1.3 c.9 - 1.4 [ 0.1 j white crappie - - - - 0.1 -- - - - i - - - - - - - - p !- Black crappie - :- -
. 0.1 - . - - - - - - - - - - - 0,3
$ Yelle* perch' O.4 0.6 0.5' O.8 0.3 0.2 - - - - - - -- 0.1 - - 0.1 ; 4 Sauger : -- - - - 0.2 - 0.1 - 0.2 - 0.1 - - 0.3
- 0.3 01 0.4 1.4 q' walleye 0.2 -- 0.3 0.3 0.3 0.2 -
0.1 0.4 0.5 - - - 0.1 - 0.1 - 0.1 ,
- Fresnwater drum - - - - - - - - -
e.2 0.2 0.1- - - ' - - - - ' - t 2 Total - 1. 8 3.4 - 2.2 3.2 2.9 'O.3-1.3 0.4 0.8 2.4 4.2 0.6 2.7 2.0 1.5 6.0 3.1 2.1 17.3 l i 1 1 4 1
+e r - + w n -s e -r, - ., v r-e'n - m a , ----n- -,w-r <- +~~e-v s~ - wr, w-----s- --u u-- - -
TABLE V-E.6E 4 -
. (Con tinne.; d.,):L Treneeet' A. 2Bs 3 !
-, species 19?4 8~ 1975b - 1976 c 3,77 d g97,4 197,4 1,gge .3,gge 1992' 1983 1984' 1995 E 1946' 1987* 1980' 1999* 1990' 1991*
~
1-
' ~
j i t .ongnose gar. - -
- , - :- - - ' <0.1- 1<0.1 -
<0.1 '<3.1 <0.1 -
0.1 ' - 0.2 Cizzard shed 0.2 0.1 -- 0.1 L -' .- (0.1 - ^- -.<0.1 0.7 .- 0.1 ' - ' Ou4- 0.0 0.1 0.3 - 0.1 0.8 nooneye . ;-- -
.. a - - ~~- - - s -u -
<0.2 - - - -
0.1' mainbow trout - -. -- - j- . northern pike
~
0.1 - < 0.1 - - <0.I' <0.1 - <0.1. <0.1 <0.1 - . i; nuskellunge ,.
- .- < 0.1 - . ' - - -
<0.1 0.1 " - < 0.1 ~ 0. 2 - -
0.1 - - ! Tiger muskellunge' - ~- - -
<0.1 -
<0.1 - --
<0.1 -
<0 1 - -
0.2 0.3 -
<0.1-
< 0.1 <0.1 Goldfish - -
0.1 - -- - - - - '- - " - - - - 0.1
. Carp 0.9 '0.3 0.2 0.6 0.3 0.3 0.2 0.3 - '0.9 0.9- 0.3 0.5 1.0 0.4 2.1 1.3 0.5 1.8
.i - ! Coldfish x Carp-0.1 0.1 hybrid'. - '- - - . e-* -
. River carpoucher - ' - - -- - ,- - - - - - <0.1 0.1 0.1 0.2 <0.1 <0.1 0.2 e
!- -Quillback' - -
< 0.1 0.2- ~0.1- < 0.1 <0.1. - <0.1 3.2 -
0.1 - -' O.1 <0.1 0.1 03 i t 3 Bighfin carpeacker ' - .- - - -- - - - -
<0.1 I~ ~ White sucker- 0.1 - -
< 0.1 - - <3.1 - <0.1 ~- -
0.1 <0.1 -
<0.1 - -
<0.1 - --
E@ Smallmouth buffalo - - -; ' - - - - - - - - - - - -
<0.1 ' -
<a.1- =c^
t. Eleck redhorse Silver redborse
< 0.1 0.1 '0.1
<0.1
<0.1 0.2 0.1
<0.1
<0.1
<0.1 0.2 5$
r* to i I River redhorse - -- - - - - -- - - - -- - - - - - -
<0.1 p, @ !
Golden redhorse 0.1 0.2 Z '
<0.1 -
<0.1 0.2 0.2 0.2 0.1 0.4
< .t'. -
shorthead redhorse - - - - - -. - -
<0.1 <0.1 0.1 - -
<0.1 0.1 0.1 - -
i W Redhorse ap. - - - - - - - - -
<0.1 -
<0.1 0.1 - - - - - 29 S4 .
1
- Black bullhead - 0.1 - - - - -- - - - - - - - - - - -
Brown bullhead Yellow bullhead 0.2 0.1
<0.1
<0.1
<0.1 -
ho 4g ;
- i. White catfish - - <0.1 - - - - - - - - - - - - - - -
>e ,
, Channel catfish 0.3 1.3 0.4 1.0 0.4 0.5 0.4 0.6 0.7 0.5 0.3 0.8 1.1 0.6 0.7 1.2 0.5 2.7 C' 2' i riathead catfish - - - - .
<0.1 <0.1 <0.1 <0.1 0.1 -
0.1 0.1 0.? 0.2 m E- [ j White bass - - - - - - ~- - - 0.1 - -
<0.1 0.1 0.8 0.3 <0.1 0.3 Q !
I Striped bass hybrid - - - - - - - - - - - - - - - - -- 2.3 O i a mock bass Green sunfish
- 0.1 -
<0.1 <0.1 <0.1~ ~ -
<0.1
<0.1 0.1 <0.1 0.2 <0.1 0.2 <0.1 <G.1 <0.1 <c.1 $ i 0.1 - - - - - - - - - - - - -
j Pumpkinseed - - - 0.1 a' - - - - . - <0.1 - - - - - - i
- Bluegill - - -
0.1 -
<0.1 <0.1 - - - - - -
<0.1 l i smallmouth bees - -
< 0.1 - - - - - - - - - <0.1 <0.1 <0.1 - -
0.2 ! i Largemouth bass 0. .' O.1 0.1 <0.1 <0.1 - - ' -
<0.1 <0.1 -
<0.1 - -
0.1 j spotted base - - 0.2 0.1 < 0.1 ' < 0.1 ~ 0.1 <0.1 0.3 1.8 0.2 0.5 0.1 0.7 2.2 1.0 0.1 1.9 { White crappie' - - <0.1 <0.1 - 0.1 0.1 -
< 0.1 - 0.2 - 0.2 -
0.1 <0.1 <0.1 -
<0.1
<0.1 0.1 <0.1
+ Black crapple - -
-<0.1 -
<0.1 - - -
0.1 - -
<0.1 -
<0.1 !
l rellow perch - 0.7 0.s 0.1 ' O.1 -
<0.1 . - <0.1 <0.1 -
<0.1 - - - - -
] Sauger' - 0.1 - 0.2 - 0.3 <0.1 0.2 0.3 0.5 0.4 0.2 0.3 0.2 0.7 0.2 0.5 0.6 ! ralleye 0.2 0.2 0.1 . 0.1- <0.1 0.2 0.1 0.7 'O.1 0.1 0.1 <0.1 - 0.2 0.1 <0.1 0.1 ; rreshwater drum - - - ~-- - ' - -
. 0.1 0.3 0.2 - -
<0.1 - 0.2 0.1 0.1 0.2 .
Total 2.2 3.1 1.5- 3.6- 1. 3 _ 1.3- 1.2- 1.5 4.4 5.2- 2.0 3.3- 3.8- 2.0- 8.1- 5.1- 2.2- 12 9- [ , . 2. 2 4.3 '1.9 ' 1. 9 1.6 4.0 4.8 3.1 8.7 5.9 2.7 13.7 [ i i
' mar. so, nov d nar- SEr.'nov i I V
C huc so nov 'nc. .im.. su. nov ( MAY- SEP MAY,.TUL SEF. DEC [
- i. +
t-___ _ _ _ _ _ _ _ _ _ . _ _ _ _ . _ _ _ ___- - ___.- - . - ._. . . . ..m, _ . , , , . . _ . .._ ,, . - _ . , _ _ _ . . _ . .
U DUQUESHE LIGilt .COMPMW 1991 ANNUAh EtWIRONMENTAh REPORT These elevated gill net catches in 1991 may indicate the trend towards improving water quality in the upper drainage of the Ohio River. How-ever, in 1991 the river conditions were favorble (low flow and limited debris) during all four of the gill net surveys, which may have contrib-uted to the high catches. Comparison of Preoperational and Operational Data Electrofishing and . gill net data, expr essed as catch-per-unit-effort, for the years 1974 through 1991 are presented in Tables V-E-$ and V-E-6. These eighteen years represent two preoperational years (1974 and 1975) and sixteen operational years (1976 through 1991) . Tish data for Tran-sect 1 (Control Transect) and the averages of Transects 2A, 2B, and 3
. (Non-Control Transects) are tabulated separately. These data indicate ,
that new species are continuing to move into the study area and that, in general, the water quality of 'the Ohio River has steadily improved. Summary and Concl1sions The fish community of the Ohio River in the vicinity of BVPS has been sampled from 1970 to present, using several types of gears electroffsh-ing, gill netting, and periodically, minnow traps and seines. The results of these fish . surveys show normal community structure based on species ' composition and relative abundance. In all the surveys since 1970, forage species were collected in the highest numbers. This indi-cates a normal fish .cor.muni ty, since game species (pr eda tor s ) rely on this forage base for their survival. Variations in total annual catch are a natural occurrence and are attributable primarily to fluctuations in the population size of the forage species. This was evident in 1991 with the abundant population of gizzard shad present in the Ohio River
~
near BVPS. Forage- species, Lsuch as gizzard shad, with high reproductive E potentials frequently respond to changes in natural environmental factnes (' ampe ti tion, food availability, cover, and water quality)- with large changes in population size. i lt 86
^
b
DUQUES!1E LICitT COMPAt1Y 1991 Atit10AL EtiVIROt1 met 4TAL REPORT Although variation in total caten has occurred, species composition has remained fairly stable. Since the initiation of studies in 1970, forage fish have dominated the catches. Carp, channel catfish, smallmouth and spotted bass, and walleye have all remained common species. Since 1978, sauger have becoine a common game spe91es near BVPS. Diff erences in the 1991 electrofishing an gill net catches, between the Control and Non-Control Transects were similar to previous years (both operational and preoperational) and were probably caused by habitat preferences of individual species. This habitat preference is probably the most influential f actor that af fects where the dif f erent species of fish are collected and in what relative abundance. Data collected from 1970 through 1991 indicate that fish in the vicinity of the power plant have not been adversely af fected by BVPS operation. F. ICl!Ti!YOPud4KTori Objective Ichthyoplankton sampling was per formed in order to monitor the extent fishes utilize the back channel 'o f Phillis I sland as spawning and nursery grounds. 9 Methods g The 1991 program had five day surveys (April 19, May 13, June 13, July _24 and August 16) and two night surveys (May 14, and July 25) con-ducted during the spring and summer, which is the primary spawning season for most resident fish species. One surface and one bottom collection were taken at Transect 2B (back channel of Phillis Island) during each survey (Figure V-F-1). Tows were made in a zig-zag fashion l across the channel utilizing a conical 505 micron mesh plankton net with a 0.5 m mouth diameter. l
\
l l 87 l
~ "*
@ .,,, m . *"'
#e .. skst!24 em=q QfNb;n raA-r+y% se=:a YEECMIDLAND j
=~
Nsagwnin vu ara ges ( 9
~
N ** %.a+.r,;p- ?^=%;qry " fD8$Uh. O k* ERUCE 3 T mesrizz.o i ew?W$m
% &.m wev~gg_ -
wi <*? n.:. . . . $ e +. rum - yo
- e. '9 Nw .* =c
- N u.y gg
>n D
an 3C AS 3 .k ,, n 7t', p yy . .- g\ ~ x 9 11 cad :l =y D1 BEAVER VAILEY DIsctARggt e ; ,* **=== 4e A ND Ma rd
.s Q D2 INDtISTRIAI. DISQtARGE e . AID TO NAVIA%
'A O 2B t
l Q g ay R N C3rf.INg i* BEAVER @ vwxt ee ns 4 STATION FIGURE V-F-1 ICHTHYOPLANKTON SAMPLING STATIONS l BVPS
DUQUESi1E LIG!tT COMIW1Y 1991 Atit10AL TJ191 Rot 1 MENTAL REP 0lfr A General Oceanics Model 2030 digital flowmeter, mounted centrically in the net mouth, was used to determine the volume of water filtered. S an.- pies were preserved in the field using Sn buf f er ed formalin containing rose !. gal dye. In the laboratory, ichthyoplankton was sor ted f rom the sample and enu-metated. Each specimen was identified as to its stage of development (egg, yolk-sac larvac, early larvae, juvenile, or adult) and to the low-est possible taxon. Densities of ichthyoplankton (numbers /100 m )3 were calculated for each sample using flowmeter data. Results A total of 74 eggs, 25 larvae, 19 juveniles and one adult were collected in 1991 from 1,619.1 m 3 of water sampled (Table V-F-1) . Nine taxa repg esenting six f amilies were identified. Freshwater drum (Aplod i not u s grunniens) eggs accounted for 35.3% of the total catch. For 1991, the night collections produced a total density of 15.22 individuals per 100 m 3 i rface and bottom samples) compared to day collections which 3 produced 4.10 individuals per 100 m . For the day coll ecti ons , the highest density occurred on May 13, with a total density of 16.39 3 individuals per 100 m (mostly unidentified eggs and carp larvae). The highest density for the night collections was on May 14, wi th a total density of 28.09 individuals per 100 m 3 (predominantly f reshwater drum eggs). tio ichthyoplankton were collected in the August 1991 survey. Comparison of Preoperational and Operational Data Species composition has remained similar between pr eoperational and operational years, while ichthyoplankton abundance has shown natural fluctuations when examined through the survey years of 1973 through 1991. The May 1991 ichthyoplankton density was the highest total for that month for the survey years 1973-1974, and 1976-1991. This year was the first time since the addition of the August survey in 1986 that no ichthyoplankton were collected for the month of August. Densities of ichthyoplankton collected in the back channel of Phillis Island (S t a tion
-2B) from 1973-1974, 1976-1991, are presented in Table V-F-2.
1
- 89. l
TAGLE V-F-1 [ NUMBER AND DENSgTY OF FISH EGGS, LAITAE, JtNENILES, AND ADULTS ~ (Number,*100 m ) COLLECTED WITH A 0.5 m PLANKTON NET IN THE l OHIO RIVER BACK CPANNEL OF PHILLIS ISLAND (STATION 2B), 1991 j BVPS [ Deoth of Collection ( Surface Bottom Total Collection l and Taxa Density g Night Dy Night Date April 19 3 126.1 139.5 265.6 _ Vol. water filtered (m ) l Number eggs collected 0 0 0 g 1 1 Number larvae collected 0 0 0 gg Number juveniles collected 0 0 gg 0 0 Number adults collected >r Density (number collected) Larva: Stizostedion sp. (YL) 0 0.72 (1) 0.38 (1) h Total Station Density gg 0 0.72 (1) C.38 (1) g g:
$ (number collected)
May 13/14 h,
>m 101.5 432.2 E 3 111.0 105.0 114.7 vol. water filtered (m )
Number eggs collected 32 22 0 2 20 5 74 21 ( g Number larvae collected i 11 0 0 -s 0 0 0 Number juveniles collected 0 0 0 0 Number adults collected 0 Density (number collected) Eggs Aplodinotus grunniens 0 20.95 (22) 0 19.70 (20) 9.72 (42) 28.83 (32) 0 0 0 7.40 (32) Unidentified egg La rvae 0 0.95 (1) 0 0 0.23 (1) Dorosoma cepedianum (YL) Dorosoma cepedianum (EL) 0.90 (1) 1.90 (2) 0 0.99 (1) 0.93 (4) Cyprinidae (EL) 1.80 (2, 2.86 (3) 0 0.99 (1) 1.39 (6) 0 0 0.87 (1) 0 0.23 (1) Cyprinus carpio (YL) 0 4.76 (5) 0 0.99 (1) 1.39 (6) Cyprinus carpio (EL) 0 0 0.87 (1) 0 0.23 (1) Morone chrysops (YL) 0 0 0 1.97 (2) 0.46 (2) Etheostoma sp. (YL) Total Density (number collected) 31.53 (35) 31.43 (33) 1.74 (2) 24.63 (25) 21.99 (95)
i
- I - ' ' 1 TABLE V-F-1
- :(Continued)
; Depth of Collection Surface Botton Total Collection Date. .g. Night- g Night and Taxa Density
' June 13:
- Vol. water filtered' .
41.9 110.5 152.4 Number eggs. collected 0 0 0 ; i; Number larvae collected' O- 3 3 - t
- i. Number juveniles collected 0 6 6 $
~
{ Number adults' collected ~ 0 0 0 Density - (number . collected) E8 f Larvae @S '
$E i- :Leposis spp.i(EL) .
0 0 - 0.90 (1) 0 0.66 ' (1) Aplodinotus qrunniens :-(EL) 0 0 1.81 (2) 0 1.31 (2) nE.. Juveniles 's c. [ Dorosoma cepedianum 0 0 5 43 (6)- 0 3.94 (6) EE i s
~$ Total Density-{ number collected) 0 0 8.14 (9) 0 5.91'(9) 3E L 6o
- - July 24/25 43-
> ~s c- > :
f i 3 ,E l Vol. water: filter *d (m ) 82.3 128.1 - 136.3' 138.6 485.3 j Number.eggsLcollecte1- 'O O O O' O y ; i Number larvae collected 0 0 0 0 0 @ ! I . Number juveniles collected 0 0 0 13 13 *
- l. Number adults collected- 0 0 0 1 1
- j Density (number collected) t
! Juveniles Dorosoma cepedianum 0 0 0 7.22 (10) 2.06 (10) Notropis sp.- 0 0 0 2.16 (3) 0.62 (3) [ Adults. ; Notropis sp.. 0 0 '0'
-0.72 (1) 0.21 (1) -
j- Total Density;(number collected)- 0 0 0 10.10 (14) 2.88 (14) i i -
.i F-i
{1 _ [ }l - - -- . . - . . - .- .. - - - - . - . - - - _ _ _ . _ - - _ _ - _ - . _ . __ :
w
' ~ E P. . (Continued) 4 .-
, ~~c Depth'of' Collection j- -Date Surface Bottom ITotal Collection j --
Day ' Might- g Night and Taxa Density-
-Auscst 16.
l Vol... water filtered (m 31- 139.1- '144.5 283.6 [: . Number eggs collected-l 0- 0 C j -- Number larvae collected' 0- 0 0 l Number juveniles. collected. 0. 0 0 ] Number adults collected 0 0. O
- .
- Density - (number collected! - '
l - Total Density -(number collected) 0 O O Yearly Totals 3 >C1 vol. water filtered (m ) , 500. 4 233.1 645.5 240.1 1.619.1 Number' eggs' collected 32: -22 0- 20 74 g cc Number larvae collected- 3 11 6 5- 25 Number juveniles collected 7. E 0- -0 6- 13 19 Number adults collected 0 'O O 1 1 n@ j Eggs J ,.
,y Aplodinotus grunniens 0' 9.44 (22) 8.33 (20) gg 0 2.59-(42) 2
. Unidentified eggs 6.39 (32) 0 0 0 1.96 (32) s9O
-Larvae "2: o
, Dorosoma cepedianum (TL) 0 0.43 (1) 0 0 0.06 (1) y% l Dorosome ce M ianum (EL) 0.20-(1). 0.86 (2) 0 0.42 (1) 0.25 (4) C' g j Cyprinidae - (EL). 0.40 (2). -1.29 (3) 0' O.42 (1) 0.37 (6) :o .< Cyprinus carpio (TL) 0 0 0.5 (1) 0 0.06 (1) E-4 Cyprinus carpio (EL) 0 2.15 (5) 0 0.42 (1) 0.37 (6)
- , Morone chrysops --(TL) 0- 0 0.15 (1) 0 0.06 (1)
Leposis spp. (EL) 0 0 0.15 (1) 0 0.06 (1) Etheostoma sp. (TL) 0 0 0 0.83 (2) 0.12 (2) '
.Stirostedion sp. (TL) 0 .l 0 0.15 (1) 0 0.6 (1)
Aplodinotus grunniens-(EL)- 0 0.31 (2) Juveniles 0 0 0.12 (2) Dorosoma cepedianus 0 0 0.93 (6) 4.16 (10) 0.99 (16)
, Notropis sp. 0 0 0 1.25 (3) 0.19 (3)
, Adults' Notropis sp.. 0 0 0 0.42 (1) 0.06 (1) 4' . Total Density . (number collected) 6.99 (35) 14.16 (33) 1.86 (12) 16.24 (39) 7.41 (119) Developmental ~S*m es
'YL - Batched specimens'with yolk ~and/or oil globules.present. ; EL - Specimens with no. yolk and/or oil globules and with no develepsent of fin rays and/or spiny elements.
I. u_ . _. . _ _ _ . . - - , _- . . _ - -. . _ , _ - _ _ - . 2 . - _ _ . _ _ _ _ . - _ _ _
DUQUESitt LICllT COMPAtlY 1991 At1NUAL Elfv!RONMEflTAL REPORT TAbl.E V-F-2 3 DENSITY OF ICllTilYOPLANKTO!J (Number /100m ) COLLECTED IN
- tile O!!IO RIVER 3ACK CilANNEL OF PilILLIS ISLAND (STATION 2D) 1973-1974, 1976-1991, DVPS Date Density Date Density Date Density 1973 1974 1976 Apr 12 0 Apr 16 0 Apr 26 0.70 May 17 0 May 24 '
May 19 0 Jun 20 16.10 Jun 13 % .98 Jun 18 5.99 Jul 26 3.25 Jun 26 2.25 Jul 2 6.63 Jul 16 59.59 Jul 15 3.69 Aug 1 6.85 Jul 29 4.05 J977 1978 1979 Apr 14 0 Apr,22 0 Apr 19 0 May 11 0.90 May 5 0 tiay 1 0 Jun 9 24.22 May 20 0.98 May 17 0.81 Jun 22 3.44 Jun 2 4.01 Jun 7 0.39 Jul 7 3.31 Jun 16 12.15 Jun 20 11.69 Jul 20 28.37 Jul 2
- 13.32 Jul 5 14.82 1980 1981 1982 Apr 23 0.42 Apr 20 1.10 Apr 19 0 May 21 0.53 May 12 0 May 18 3.77 Jun 19 9.68 Jun 17 26.40 Jun 21 7.54 Jul 22 107.04 Jul 22 17.14 Jul 20 31.66 1983 1984 1985 Apr 13 0 Apr 16 0 Apr 18 0 May 11 0.66 May 10 0 May 14 1.01 Jun 14 4.46 Jun 8 15.46 Jun 10 13.36 Jul 12 44.05 Jul 12 44.23 Jul 11 117.59 1986 1987 1988 Apr 18 0.63 Apr 21 0 Apr 18 0 May 13 a 5.93 May 19 8 16.22 May 10 8 0.42 Jun 19 34.52 Jun 19 40.02 Jun 14 162.43 8 a Jul 15 26.15 Jul 14" 19.26 Jul 14 39,41 Aug 12 9.89 Aug 10 7.87 Aug 16 1,32 1989 1990 1991 Apr 13 0 Apt 18 0.37 Apr 19 0.38 May 23" 0.91 May 24 a 2.15 May 13 a 21.98 Jun 19 25.50 Jun 12 20.67 June 13 5.91 Jul 25 a 8
.Jul 12a 438.61 2.91 Jul 24 2.88 Aug 15 4.20 Aug 21 6.09 Aug 16 0 l , 1
- Day and night survey was conducted. I l
93 l
DUQUCSilt LIGitT COMPAlly 1991 AflMUAL ENVIRONMENTAL llCPORT Summary and Conclusions Gizzard shad and freshwater drum dominated the 1991 lehthyoplankton catch frcrn the back channel of Phillis Island. The peak density occurred in May and consisted mostly of eggs. The month of April showed little spawning activity. The ichthyoplankton densities for June and July were lower than mos t of the previous totals for those months reported in previous-survey years. G. FISH IMPI!!GEMENT i l Objectig i I Impingement surveys were conducted to monitor the quantity of fish, f other aquatic organisms and Corbicula ~ impinged on the traveling screens. These surveys were also conducted to monitor for the potential infesta-tion of the Zebra mussel.
- Methods The surveys were conduc ted weekly throughout 1991 for a total of 42 weeks (Table V-A-1) . Except when technical dif ficul ties delayed the l start of collections, weekly fish impingement sampling began on Thursday !
mornings when all operating screens were washed. A collection basket of 0.25 inch mesh . netting was placed at the end of the screen washwater sluiceway (Figure V-G-1) . On Friday mornings, after approximately 24 hours, each screen was washed individually for 15 minutes tone complete r evolution of the screen) and all aquatic organisms collected. Fish were identified, counted, measured for total length (mm), and weighed (9 ) . Data _ were summarized according to operating intake bays (bays that had pumps . operating in the 24 hour sampling period) and non-operating intake bays. ' 94
DUQUESt1E LIGIIT COMPANY 1991 AttrlUAL Enytnor: MENTAL REPORT
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1 (Two dimentional: Side View) l FIGURE V-G-1 i INTAKE STRUCTURE BVPS 1 95
DUQUESNE L1GitT COMPANY 1991 ANNUAL 1:NVIRONMEldTAL REPORT Results The BVPS impingeLent' eys of 1976 through 1991 have resulted in the collection of 42 s pe c.. of fish representing ten families (Table V-G-1). A total of 260 f.shca, repr esenting 19 species were collected ; in 1991 (Table V-G-2) . The striped bass hybrid and sauger, which had not been collocted in previous years, were both collected in 1991. Freshwater drum were the most numerous fish, comprising 39.3% of the total annual catch, followed by gi zzard shad (16. 5% ) , bluegill and carp (11.2% each). The fishes ranged in size f rom 15 mm to 257 mm, with the majority under 100 mm. The total weight of all fishus collected in 1991 J was 2.2 kg (4.6 lbs) . No endangered or threatened species were col-(. lected (Commonwealth of Pennsylvania, 1985). The 1991 impingement catch t
.is comparable to catches of previous years (1976 to 1990) (Tables V-G-3 and V-G-4) . During each year, generafly the largest numbers of fish have been collected in the winter months (December-February) and then the catch has gradually decreased until the late summer period when another, smaller peak has occurred.
Other organisms collected in the impingement surveys include 10I cray-fish, 6? native clams,. and 95 dragonflies (Tables V-G-6 and V-G-8) . In addition, .1,986 Asiatic clama (Corbicula) were collected - (Table V-G-7) . Comparison of Impinged and River Fish < A comparison of the numbers of fish collected in the river and traveling screens is presented in Table V-G-S. Of the 40 species collected, 16 l were observed in both locations, three species were collected only in the impingement surveys, while 21 species were collected exclusively in the river. The major dif f erence in species composition between the two
~
types- of collections is the absence of large species in the impingement ' collections. There were nine species of suckers and six game fish species which were collected only in the river studies. Game fish which were collected on the traveling screens (channel catfish, flathead catfish, white bass, rock bass, bluegill, smallmouth and largemouth l, t I-l :96.
DUQUCSilE LIGitT COMPAliY 1991 Attr10AL EttvinorantnTAL REPORT TABLE V-G-1 FJSH COLLECTED DURING THE IMPINGDiD3T SUPVEYS, 1976-1991 DVPS Family and Scientific Hame l Common Hame Clupeidae (hcrrings) Dorosoma cepedinnum Gizzard shad Cyprinidae (minnows and carps) Cyprinus carpio Common carp flybops,is storerlana Silver chub Hotemigonus crysoleucas Golden shiner Notropia atherinoides Emerald shiner
- 11. hudsonius Spottall shiner
- 11. jspilopterus Spotfin shiner N. tetramineus Sand shiner H.Iolocellust Mimic shiner
. fim'hphalesnotatus Bluntnose minnow P2 ,promelas Fathead minnow
_Semotilus atromaculatus Creek chub Catectomidae (sucLers) Carpiodes cyprinus Quillback Catostomus commersoni White sucker Hoxostoma carinatum River redhorse 1ctaluridae (bullhead and catfishes) Ictalurus catus White catfish J,. natalia Yellow bullhead J,. nebulosus Brown bullhead J,. punctatus- Channel catfish Notorut flavus Stonecat pylodictis olivaris Flathead catfish Percopsidae (trout-perches) percopsis omiscomaycus Trout-perch Cyprinodontidae (killifishes) Fundulus diaphanus Banded killifish Percichthyidae (temperate basses) Morone-chrysops White bass _11. chrysops-x pl. saxatilis Striped bass hybrid 97 , 1 j
DUQUBSNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT i t TABLE V-G-1 (Continued) Family and scientific Namel Common Name Centrarchidae (sunfishes) Ambloplites rupestria Rock bats Lepomis cyanellus Green sunfish L. gibbosus Pumpkinseed L. macrochirus Bluegill Micropterus dolomieul Smallmouth bass M. punctulatus Spotted bass M. salmoides Largemouth bass Pomoxis annularis White crappie P. nigromaculatus Black crapple Percidae'(perches) Etheostoma nigrum Johnny darter E. zonale Banded datter Perca flavescens Yellow perch Percina caprodes Logperch P. copelandi Channel datter Stirostedion canadense Sauger S,._ vitreum vitreum Walleye Sciaenidae (drums) Aplodinotus grunniens Freshwater drum Nomenclature follows Robins et al. ~(1980) w 98.
r - U ] r
.g -
.l SUMERY OF FISH COLLECTED IN IMPINGEMDrr SURVEYS CONDUCTED FOR ONE 24-HOUR PERIOD .l PER WEEK ' DURING.1991
~ BVPS"- .j
. OPtamTtuC INTart marsl ups-OFEmmTtWC Tw-ARE 84YS 2 , Percent Aliee Dead Aliee Dead 1,ength Fregeency Percent i . Wesght weignt wesgat w,agnt - mange -. 4
*ame womber . Occurrence - Ccumposition ' Number ' fg) Nimmber fg1 - number' M Niseber - tg) fgs 5 -
Cizzard shed . 43 - 21.4 16.5 41 534 .2 25 40-200 ? l .. Carp 29' 11.9 11.2 2- 5. 2 2 12 42 13 17 21-75 i' amerald shiner 1 '2.4 0.4' 1 1 , 56 ' e Bluntnose minnow L 1 ,. 2. 4 0.4 1 . 5 31. - * + e.* k Channel catfimh' .2 4.8' O.8 1~ 4 1 5 's;-92 O zoC-l 1rlathead catfish 4 7.1 1. 5 2 21 2 2 55-110 CC i
>M t* to j
[- White bass -8 14.3- 3.1 '3 15 5 214 .30-z43 2 i
- c. 29 M
. Z r Striped bass hybrid 1 2.4 0.4 1 150 220 < t*
w i 2p G e i' { e Rock bass.. 28 33.3 10.8 18 78 4 109 3 11 3 2 25-175 - gg. l- 3 > Creen sunflah - 1 2.4 0.4 1 2. SS rg O 0.4 1 10 85 h>7'
- k.
'Pumpkinseed 1 2.4 "D
l Bluegill 29 29.4 11.2 11 27 17 32 '1 1 25-95 W n v 5 smallmouth bass 1 . 2. 4 0.4 1 78 17s o 4 Spotted bees 1 2.4 0.4 1 10 92 1.argenouth bees 1 2.4 0.4 1 232 257 ! Banded darter 2 4.s 0.8 2 3 40-40 j togperen 2- 4.8 0.5 2 4 55-81
- . Sauger 3 2. 4 1.2 3 25 110-115 i
l Freshwater drum 102 35.7 39.2 29 ~ 107 32 196 17 43 24 79 15-120 l Total 263 71 592 111 1.196 36 2 50 42 123 Intate bays that had pumps' operating within the 24-hoer sampling period. Intake bays that had na pumps operating witSin the 24-hour sampling period.
, , m . . ,.' ,~.4..,.,, .,.m. ... - *.m-.- . - -.s. . i..... _ ~..,._J...-, m,._. - . . ._ __. - . , , _
m .. - 4 TABLE.V-G-3
SUMMARY
OF IMPINGDIENT SURVET DATA FOR 1991 BVPS operating Ison-operating Intate Bays Intate River Elevation Date it;aaben 91 Fish Percent fatane Bars 1 Intate Says 2 Operating Water Above i4ean Montn g co1 M ted Annual Total Alive Dead .Aliv. Dead A a c o Temp *r see t.evel frt.) January 4 II ' - - 39.2 572.8 11 0 0.0 x x x x 38.2 668.8 18 1 0.4 1 1 2 x 0 40.0 672.5 25 0.0 x x x x 35.5 667.0 February 1 0 0.0 X' X X X 35.6 8 0 0.0 .I x 1 39.1 667.8 670.0 [up 15 0 0.0 x x X 37.2 669.2 22 0 0.0 1 1 1 37.8 671.3 2' T3 ZC Maren 0 Zo 1 1.0 X x I 38.9 667.0 CC 8 0 0.0 15 0 0.0 1 2 1 X 41.2 673.3 c- ::$ X X X 39.4 667.9 22 0 0.0 45.0 X X X 467.0 m 29 2 0.8 1 1 X X X 50.2 667.4 $[ 72 0
$ April 5 I 12 II 50.1 665.5 @h 55.3 666.1 ~K
' 19I8I - -
55.1 666.3 26 I83 "zO 53.0 667.0 y (. r* > May 3 0 0.0 K I 1 61.0 666.1 2 10 0 0.0 x 17,t 5) I 1 61.7 665.8 N 3 72.0 665.8 24*"I - - - - - - 74.0 665.7 :n 31 3 1.2 2 1 1 E 1 79.4 665.9 d i June 7 15 5.8 1 2 12 x x X 78.4 665.8 14 t5) - - - - - - 78.8 660.5 21 ts) _ _ _ _ _ _ gg,g _ 28 25 9.6 4 11 6 4 x x x 81.1 665.7
%. __ = -
f i TABLE V-G-3 " (Continued) Operating Intake Bays Date Number of Fish Percent Non-Operatigg Intake River Elevation Intake Bays Intake Bays Operating Water Above Mean Month Osy, - Collected Annc31 Total ~ Alive Dead Altve Dead A C D Temp O r B Sea Level (Ft.? July - 5 19 ~ 1.3 '7 5 4 3 x -X X 83.0 666.0 12 46 17.7 6 10 14 16 1 X X 79.9 665.5 19' - 16 ' a.2 7 1 3 5 X- X X 79.9 663.0 26 6 2.3 5 1 X X X X 81.8 665.0 August .2 3 1. 2 1 2 X X X X 78.0' 665.2 9 3 3.1 5 3 X X X X 78.8 665.0 16 6. 2.3 4 2 X X X X 77.0 664.8 Em 23 3 L' 2 1 1 1 1 X 76.3 665.0 30 4 1.5 3 1 X l3 X X X 79.0 665.c ED
-C September 6 1 0.4 1 1 X X X 77.2 665.0 Z K) 13 5 1. 2 2 1 % K X 3 75.5 665.0 20 1 0.4 1 X X
$3 h X X 70.0. -665.0 27 0 0.0 C' &!
X X X X 66.9 665.0 n; $3 Z Octobe r 4 2 0.8 1 1 X X X
- p. t'.
X 66.0 665.0 m 11 5 1.9 3 1 1 X X X 62.9 665.S M 62 [j 18 2 0.8 2 1 I X 58.0 666.2 5 25 0 '0.0- X X 57.9 665.0 Jn ZO November 1 2 0.8 1 1 : X 58.1 665.2 3 55 8(5) - - - - - - 52.0 665.0 C* > 15 3 1.2 3 X- X X es.! 664.6 3! 22 3 1.2 2' 1 X X X 48.2 654,6 29 1 0.4 1 1 X 45.1 664.4 C)
- p H
December 6 67 25.8 11 54 2 X X X 41.3 666.0 13 12 4.6 2 9 1 1 X 43.5 665.8 20 1 0.4 1 X X 37.2 665.0 27 0 0.0 I X 37.4 665.8 Total 260 71 111 36 42 1
, Intake bays that had pumps operating in the 24-hour sampling period.
Intake bays that had no pumps cperating in the 24-hour sampling period. 3 Impingement could not be conducted due to high water conditions. fImpingementcouldnotbeconductedduetodivingoperationsinscreenhouse.
' Impingement ould not be conducted due to maintenance.
r _m___
TABLE V-G-4
SUMMARY
OF FISH COLLECTED IN IMPINGEMENT SURVEYS, 1976-1991 BVPS
-Number of Fish Collected Unit 1 1978 1979 1980 1981 i 1976 1977 Oper N-Oper Total Oper N-Oper Total O m N-Oper Total Oper M-Oper Total Month Oper III N-Oper Te la). Oper N-Oper Total 16 82 5 0 5 5 1 6 l 1,136 -2,869 4,005 186 41 227 66 January 3,792 2,021 % 813 5 7 12 21 1 22 3,622 2,039 5,661 99 73 372 9 8 17 February 1,087 1,034 2,121 29 4 2 6 36 113 149 15 10 25 16 13 260 128 388 314 72 386 Maren 1 4 1 0 1 0 11 11 8 0 8 11 30 7 3 10 3 ~
April 19 4 0 2 2 7 2 9 e 0 3 - - - 3 1 my 5 2 7 3 0 3
- 6 2 0 2 0 4 4 3 "
5 4 3 7 2 4 June 4 1 7 3 10 13 5 2 7 32 9 3 12 5 2 July 20 12 32 27 5 12 13 >0 34 54 10 4 14 1 August September 27 8 10 6 37 14 6 1 1 4 7 5 6 7 12 15 18 22 20 9 9 18 4 0 4 15 10 4 2-19 12 CC 14 18 21 6 27 2 2 4 October 35 8 43 8 3' 11 4 2 3 7 6 13 3 1 4 4 0 4 h$ November 15 374 219 4 19 593 9 174 0 12 9 186 1 20 3 23 3 4 12 6 0 6 28 4 32 gy December 3,456 9,102 5,311 5,011 10,322 373 261 654 162 100 261 54 54 108 122 .19 141 [ Total 5,646 M9 O 5 N x Number of Fish Collected Unit 1 1976-1996 Ave.
]h
>4 ;c 1984 1985 _ _ __ 1986 >m 1982 1983 --
III N-Oper II Total Oper N-Oper Total Ooer N-Oper Total Opar N-Oper tsJ Oper, N-Oper Total Oper N-Oper Total Iy Month Oper 939 g ,< 2 90 4 94 487 4 52 y 44 9 0 9 34 5 39 4 Jsnaary 30 16 11 19 11 30 2 0 20 2 22 447 293 740 o 66 10 1 February 24 42 7 11 5 5 10 23 7 30 3 + 4 7 6 3 9 62 33 95 10 March 4 15 4 19 0 0 0 1 0 1 6 4 6 9 11 7 18 5 April 3 0 2 0 1 1 4 1 2 16 3 19 4 2 5 2 May 1 1 2 0 3 3 2 2 4 9 7 2 9 1 1 0 2 2 3 6 June 0 4 6 1 7 10 4 14 1 3 4 27 2 29 July 4 5 7 3 3 6 10 7 17 7 7 1 8 4 3 14 0 14 2 5 7 8 6 14 August 0 4 4 8 4 12 3 4 16 16 13 29 September 13 3 0 0 0 8 9. 17 18 4 22 12 6 18 12 19 15 8 23 Octcber 7 1 1 2 70 10 80 26 1 27 14 3 11 8 9 9 18 November 4 4 25 14 0 14 65 24 89 10 59 0 2 2 24 1 December 16 9 25 /3 164 187 26 213 1,127 835 1,962 446 'O 216 137 40 177 130 34 Total 120 107 227
m TABLE V-G-4 (Continued)- Nurnber of Fish Collected Unit . and Unit 2 1987 1988 . 1989 1990 1991 1987-1991 Ave. Month Cper NI N-Oper I23 Total _Oper K-Oper' Total 'Oper .N-Oper Total' Oper N 4per Total Oper N-Oper Total Oper N-Oper Total. g ' o. January 242 0 242 25 4 29 387 4- 391 16 0 16 1 0 1 134 2 136 yS Februa ry 27 l' 28 5 1 6 34 1 35 0 0 0 0 0 0 13 1 14
' March 5 4 9' 2 2 4 70 8 78 2 1 3 2 0 2 '16 3 19 %9 April 4 1 5 12 -1 13 7 1 8 1 1 2 - - -
6 1 7 Eb May June-3 1-0 1 3 2 0 2 0 0
-0 2
1 2 1 0 2 2 0 2-1 1 3
- 1. 2 16 1
24 3 40 1 5 1 5 2 10 c- La July 11 1 12 63 0 63 -5 0 5 2 1 3 42 45 87 25 ? ' 34 g y August 11 J 12 24 27 51 12 0 12 16 -0 16 24 0 24 17 6 23 Z September 10 0 10 12 3 15 3 4 7 10 2 -12 5 0 5 8 '2 10 $C
>' Oc 'ber 0 1 1 3 0 3 1 6 7 . 1 1 2 5 4 9 2 2 4 mn O '41 9 November 0 1 1 29 12 2 0 2 5 0 5 8 1 9 3 12 3 % ,
Decen;be r 20 0 20 247 7 254 0 1 1 5 0 5 77 3 80 70 2 72 3
$O Total 334 11 345 424 57 481 524 26 550 60 9 68 182 78 260 306 37 343 yg r>
=.
N I Intate bays that had pumps operating in the 24-hour sampling period. ]. Inttke bays that had no pumps operating in the 24-hour sampling period. x d symbols Oper - Operating intske bays. N-Oper - Non-operating intake bays. o t e
,a --
ae=..=_--
-DUQUESNE LIGliT COMPANY 1991' ANNUAL ENVIRONMENTAL REPORT.
i TABLE'V-G-5
' NUMBER AND- .RCENT OF. ANNUAL TOTAL OF FIS!! COLLECTED IN IMPINGEMENT SURVEYS . AND-IN THE NEW CUMBERLAND POOL OF THE 01110 RIVER, 1991 BVPS Total- Number of
~
Percent of Fish Collected Annual Total Speci es (a) Impingement -River Impingement River Longnose gar 5 0.1 Gizzard shad 43 2,903 16.5 84.2 Mooneye- 3 0.1 Rainbow trout. 1 0.1 Tiger muskellunge 4 0.1 Central stoneroller 1 0.1 "oldfish.
, 2 0.1 Common carp- 29 89 11.2 2.6 Silver chub 3 0.1 Emerdid shiner 1 31 0.4 0.9 Mimic - s hiner 1 0.1 Bluntn'ose minnow 1 0.4 River carpsucker 7 0.2 ?Quillback 15 0.4 M High fin- ca r ps ucker - 2 0,1 Harthern hog sucker 2 0.1 Smallmouth buffalo- 2 0.1 -dilver redhorse 9 0.3 River redhorse 2 0.1 , Golden.redhorse' 27 0.8 Shorthead redhorse: 2 0.1 - Chtanel catWh 2 85 0.8 2. 5 'Flethead catfish: 4 9 1.5 0.3 White bass 8 40 3 .' l 1.2 Striped bassihybrid. 1 70 0.4 2.0 Rock bass: 28 3 10.8 0.1 . Green sunfish' 1 1 0.4 0.1 Pumpkinseed 1 0.4 Bluegill -29 3 11.2 0.1 Sm:11 mouth. bass 1 1 22 0.4 0.6 Spotted bass' 1 57 0.4 1.7 L rgemouth; bass 1 4 0.4. 0.1 White crapple 1 0.1 Bitck crapple 3 0.1 -B nded darter 2 0.8
- Yellow perch 1 0.1 Logperch 2 3 0.8 0.1 Stuger. 3 25 1.2 0.7 Walleye. 4 0.1 Freshwater-drum 102 6 39.2 0.2
. Total 260 3,448 l
(a) Includes only those specimens identified to species or stocked hybrids. 104
DUQUESNE LICllT COMPANY 1991 ANNUAL.ENV!RONMENTAL REPORT TABLE V-G-6
SUMMARY
OF CRAYFISil COLLECTED IN IMPINGEMENT SURVEYS
, CONDUCTED FOR ONE 24-ilOUR PERIOD.PER WEEK, 1991 BVPS Number Collected operating Non-Operating Date Intake Bays ~ Intake Bays Month Dg Alive Dead Alive D,e a d, January 4 (a) , , . .
11- 9 0 0 0 10 2 0 0 0 25
~ ,, 2 0 0 0 February. 1 5 0 0 0 B 2 0 1 0 15 2 0 0 1 22 0 0 1 0 March 1 3 0 0 0 8 0 0 0 0 15 0 0 1 0 22 1 0 1 0' '
29 1 0 0 0 April S ID) - - - - 12(b) . . . _ 19(b)- , . . , 26(b) . _ _ , May 3- -0 0 1 0 10 0 0 0 0 17 (C) . . _ _ 24 ICI - - - - 31 0 2 0 0
-June 7 0 1 0- 2 14 (c) . . . .
21(c) . . _ _ 28 1 3 0 0
-July 5 4 0 1 0 12 6 0 0 4 19 1 0 2 0
-26 8- 1 0 0 August 2 2 0 0 0 9 0 1- 0 0 16 3 0 0 0
- 23. 0 0 0 0 30 1 1 0 0 105
.DUQUCSNE LICllT. COMPANY-
-1991' ANNUAL ENVIRONMENTAL REPORT TABLE V-G'6 (Continued) l i t '.
Nt G r Collected Operating Non-Operating Date Intake Bays Intake Ba g . Month Day Alive Dead Alive Dead
- September- 6 0 0 0 0
- 13 . 0 1 0 0 20 l~' O O O
=- 2 7 0 -1 0 0 l
October .4 'O 2 0 0 l 11 0 1 0 0 i 18- 0 0 0 0 l 25 1 1 0 0 - I November l - 0 0 0 0 B ICI - - - - 15-0 1 O O 22 0 0 0 0
=29 2 0 0 0
" Dscember= 6 3 0 1 0 4 13 1 0 5 0 -I
- 20. 1 0 1 0 27 4 0 0 0
- Total. 66 16 15 7
' I*I' Impingement-Jcould not~-be_ conducted due to high water conditions.
(D) impingement'could.not be conducted due to diving operations in screenhouse.. CI Impirgement could'not be. conducted due to maintenanco 6 1 106
DUQUESNE LidliT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT-TABLE.V-G-7
SUMMARY
OF Corbicula COLLECTED DURING IMPINGEMENT SURVEYS FOR ONE 24 .909R PERIOD PER WEEK, 1991 BVPS Number Collected Operating Non-Operating Date Intake Bays Intake Bays Month Day plive Dead Alive Dead January 4(a) _ _ _ _ 11 0 0 0 0 18 0 0 0 0 25 0 0 0 0 February 1- 0 0 0 0 8 0 0- 0 0 15 0 0 0 f 22 0 0 0 0
' March 1 0 0 1 0 o 8. 0 0 0 0 15 0 0 0 0-
. . , 22 0 1 0 1
'"?' 29. 2 2 0 0
!!s:
il April: 5(bs _ _ _ _ 12 (b) . . . . 4 7 f. _ _ _ _
-19((b) 26 b) . _. _ _
May 3 65 74 0 t 10 0 15 0 3 17(CI~ - - - - 24(C) - - - - 31 2 9 0 8 June 7 3 7 0 2 14(c) . , _ _
- 21 (c) _ _ _ _
28- 6 13 1 1
' July 5 -1 10 13 3-12~ 44 18 12 10 19 45 8 6 1 26 113 30 0 0 107
^1 DUQUESNE LIGilT COMPANY L 1991' ANNUAL ENVIRONMENTAL REPORT-1 TABLE V-G-7 (Continued)
.,. - Number Collected Operating Non-Operating Date _ Intake Bays Intake Bays Month Day Alive Dead Alive Dead August- 2 14 57 0 0 9- 77 137 0 0 ' 16- 78 22 0 0 23 5 36 0 0
=30 28 30 0 0 September- 6- 68 89 0 0 13 79 37 0 0 20 80 16 0 0-27 45 7 0 0 z .
October 4 -45 55 0 C 11- 18 20 4 2 18- 6 17 2 7 25 9 4 6 2 Nov.mber- 1 - 2 6 5 4
- 8 ICI - - - -
15 47 25 0 0 22 -7 6 0 0
-29 -4 42 6 '84 Dscember 6 0 19 0 20, 13 0 9 0 4 20 0 5 0 3
-27 1 3 0 2
' Total 942 829 56 159 I"I .Tmpingement coul'd not be conducted due to high water conditions.
.(b)-Impingement-could not be conducted due to diving operations in screenhouse.
ICI Impingement could not be conducted due to maintenance. 1 ) ! 108
i DUQUESNE LIGitT COMPAllY !1 _ 1931 AllNUAL ENVIROtiMENTAL REPORT TABLE V-G-8'
~
SUMMARY
OF MOLLUSI'.S - (OTHER THAN Corbicula) AND DRAGONFLIES COLLECTED IN IMPINGEMENT SUrWEYS CONDUCTED FOR ONE 24-HOUR PERIOD PER WEEK, 1991
% DVPS~
Date Number of Otganisms in-all Bays _ Month Day Mollusks Dragonflies January 4 (a) , , 11' 0 0 18 0 1
-25 0 0 February l_ 0 0 8 0 0 15 0 0 22 0 0' March 0 0 8 0 0 15 0 0 22- - 0 0 29 0 4
-April S IDI - -
12 (b) .. _ 19 (b) _ _
'26(b) . _
Mey - 3. 0 0 10 1. 0 17 (C)_ - - 24(c)- . _ 31'- 0 2 June- 7- - 0 0 14(c) _ _ 21(c) _ _ _ ,
' 2 8 -- 0 0- E July 5 0 1 12 0 2 19 0 1
- 26. :7 0 109 l
DUQUESNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT TABLE V-G-8
' (Conti nued)
Date- Number of Organisms in all Bays Month Day _ Mollusks Dragonflies August '2 6 0 9- 9 2 16 16 2
-23 6 2 30 1 2 September 6 1 4 13- 3 6 20 0 8 27 0 8 October 4 0 20
'll 2 7
.18 0 10 25 0 2 November- 1 4 1 8 ICI - - -
'15 3 5 22 0 0 29 1 2 December 6- 1 0
, 13' 1 3 20 0 0 27 0 0
' Total- 62 95 I"I ~Impingemest could not be conducted;due to high water conditions.
(b) Impingement'could not be conducted due to diving operations in (c) ;screenhouse.
=
_1mpingement'could not b'e conducted due to maintenance. 110
DUQUESNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT bass, and spotted bass) were smaller than individuals of those species collected by-river sampling. Comparison of Operating and Non-Operating Intake Bay Collectiong Of the 260. fishes ' collected during the 1991 impingement studies, 182 (70.04) were collected from operating intake bays and 78 (30.0%) from non-operating intake bays (Table V-G-2) . However, due to differences between the number of oper ating (126) and non-operating (24) screens washed in 1991, the impingement data were computed with catch expressed as fish per 1,000 m 2 of screen surface area washed. These results 2 showed 8.1 and 18.2 fish /1,000 m for operating and non-oper a ti ng
- screens, respectively. As in previous years, the numbers of f'ish cc,1-l lected in non-operating bays indicate that fish entrapment, rather than impingement, accounts for some of the catch. Entrapment occurred when fish were li"ted out of the water on the f rame plates as the traveling screen rotated. Alternatively, impingement occurred when fish were forced against the screen due to velocities created by the circul'ating water pumps.
Of ~ the - 104 crayfish collected in the 1991 impingement . studies, 82 (78.9%) were collected f rom operating bays and 22 (21.11) were collected
~
- from r in-operating bays (Table V-G-6). Adj usting these data for screen surface area washed (crayfish per 1,000 m2 ) the results show 3.6 and 5.1 crayfish for operating and non-operating screens, respectively.
Corbicula collected in the 1991 studies included 1,771 (89.2%) in the operating bays and 215 (10.8%) in the non-operating bays (Table V-G-7) .
- Again, adj us ting . th ee data for the screen surface area washed 2
(Corbiculs per l',000 m ) the results show 78.8 and - 50. 2 Cor bicula for operating and non-operating screens, respectively. Summary and Conclusions The results of the '1991 impingement surveys indicate that withdrawal of r. river water at the BVPS intake for cooling purposes has very little 111
q DUQUESNE LIG!!T COMPANY:
-1991 ANNUAL? ENVIRONMENTAL REPORT et f ect - on' the 1 fish populations.; Two: hundred sixty (260)- fishes were-
. collectedi which ::: was -- comparable 1 to other = yearly totals since int tial operation,of BVPSLin"1976. -Freshwater drum were-the:most numerous fish, l comprising . 39. 2%.t of ..the1 total - annual-- catch. The total weight of all fishes collected. in 1991 was ' 2.2 kg L.. (4.8 lbs). - Of the - 260- finhes c; l-s lected, 107 6 (41. 2%) were -alive and ~ returned via the . discharge pipe to the Ohio River..
H.- PLANKTON ENTRAINMENT ' f.
.l. Ichthyoplankton objectives -
- l
.The ichthyoplankton Tentrainment studies are designed to determine the species 1 composition, relative abundance, and. distribution of ichthyo- -
plankton found in- proximity to the BVPS ' intake structure. 4 Methods-1; Previous studies have ' demonstrated that species composition and eelative
- abundance E of j ichthyoplankton samples ~ collected in fronti of the intake
---structure were very'similar:to those'ichthyoplankton entrainment samples.
- taken' at BVPS (DLC ' 197 6,- .1977, 1978, and 197 9) . - Based-on these results, 1
- a: modified- sampling program was utilized from 1980 ' tnrough - the current :
sampling season . which sampled the.. Ohio River along a ' transect adjacent to J thea BVPS --- intake. ' structure -(Figure-- V-F-1) . - Samples were : collected monthly,,from April through August,- _ during daylight hours along a " five U station transect. . Night' collections were made in May and' July. Surface
- tows were made at Stations 1, 3,, and 5 . and bott.om tows were t taken at
{ Station L 2 and 4 utilizing 'a15051 micron mesh plankton net with a 0.5 m
~ diameter . mouth.- Sample - volumes were measured by a General. Oceanics .
/ Mcy3e1 2030.' digital- flowmeter mounted . centrically. in the mouth of the net.: Samples were preserved upon collection ? in 54 buffered formalin containing rose bengal dye.
L h) 112
~- DUQUESNE LIGHT COMPANY 1991 ANNUAL E!NIRONMENTAL REPORT In the laboratory, eggs, larvae, juveniles, and adults were sorted from the samples, identified to the lowest possible taxon and stage of devel-opment,- and enumerated. Densities of ichthyoplankton (number /100m 3) were. calculated using appropriate flowmeter data. Results, A total of 260 eggs, 188 larvae, 13 juveniles, and one adult represent-ing eleven taxa and seven families were collected frcn 3,750.1 m 3 of water - filterad during sampling along the river entrainment transects (Table V-H-1) . Freshwater drum, Cyprinidae spp., and gizzard shad were the mos t' common '.axa , representing 26.8%, 14.5%, and 11.5% of the total catch respectively. The larvae collected were predominantly gizzard shad, . cyprinids, and ca r p. - Juveniles only made up 2.8% of the total ichthyoplankton catch. One adult (log perch) . was collected during the July 25 (night) survey.
- Seasonal Distribution The initial survey of April 19, 1991 collected six ichthyoplankton larvae - (Table V-H-1) . No eggs were collected in the April survey. The May survey collection was the highest for the year with- 155 eggs (p r e-dominantly f reshwater drum) and-149 larvae, ccmprised mostly of uniden-tified cyprinids, ca r p, and gizzard shad. Total density of ichthyo-3 plankton -(individuals /100 m ) in May '(day and- night surveys combined) was 25.30/100 m3 . The May night survey total density was almost three
.. times greater than the day survey, with calculated totals of 13. 56 a...;
37.34 individuals /100 m3 , respectively. June had a lower ichthyoplankton density of 8.02 individuals /100 m .3 The July (day and -;ght surveys' combined) total ichthyoplankton density was almost 2. 5 times lower than the May total- density, with a density of 10.59 individu als/100 m3 . The July collection was dominated by eggs (84.9%). The August survey collected eggs only, with a total density of 3.87 eggs /100 m3 . 4 113
1i uTAB3.E V-H-1 NUMBER AND DENSITY OF FISH EGGS, LARVAE, JUVENILES,'AND ADULTS (Humber/100 m )~ COLL".CTED WITH A O.5'm PLANKTOt1 NET-
' AT THE ENTRAIN!iENT RIVER TRANSECT IN THE OHIO RIVER, 1991 BVPS-
.Doce ' Station 1 Total Station 2 Station 3 Station 4 Day, Night g Niqht g Station $ _ .. Collected and-
. Nis ,t Dg Night :Dy Night. Taxa Density April 19 voA. wate; filtered (m 3) 124.7 13 6.9 115.3 127.7^ 107.3 611.9 Mumber eggs collected 0 , 0 0 0 0 Number larvae collected: 4 0
1 0 1 0 6 Number juveniles collected 0 0 'O O O *' O Number adults collected. . 0 0 0 0 0 0 Density (number collected) gg-Larvae 2". so - Stirestedion sp. (YL) 3.21(4) 0.73(1) 0 0.78(1) Total Station Density 3.21(4) 0.13(1) O C.78(1) 0 0 0.98(6) 0.98(6i
~$$
t* to - (number collected). ' y. May 13/14 p $[
- o O 3
w vol. water filtered tm ) 107.8 101.9 154.8 153.7 O Number eggs collected 32 29 4 18 108.3 114.8 33 146.6 2 133.9 79.7 100.1 1,201.6 8N Number larvae collected 0 22 6 8 3 6 18 15 24 27 9 1 43 155 %g Number juveniles collected 0 0 0 0 0 0 0 0 4 149 zo 0 Numoet adults collected 0 0 0 0 0 0 0 0 0 0 0 0 0'
- " g Density (number collectedi Eggs q Aplodinotum grunniens 0 22.57!23) 0 9.11(14) 0 15.68(18) 0 16.43(22) 0 1.00(1) 6.49(78) 3 Unidentified egg 29.68(32) 5.89(6) 2.58(+) 2.60(4) 2.77(3) 13.C7(15) 1.36(2) 1.49(2) 11.29(9)
Larvae 0 6.41(77) .g Dorosoma cepedianus (YL) 0 0 .0 0.65 (1) 0 0 0 0 0 Dorosoma cepedianum (EL) 0 1.00(1) 0.17(2)' 0 0.65(1) 0 0 1.74(2) 2.73(4) 7.47(10) 0 4.00(4) 1.75(211 Cyprinidae (TL) 0 0 0 0 0 D. 97 (1) 0 0 0 Cyprinidae (EL) 0 0 0.08(1) 14.72(15) 0.65(1) 0.65(1) 1.85(2) 2.61(3) 2.73(4) 1.24(3) 3.76(3) 33.97(34) 5.49(66) Cyprtnus carpio (YL) 0 3.93(4) 2.58(4) 0 2.77(3) 6.97(8) 4.09(6) 2.24(3) 1.25(1) -0 2.41t291 Cyprinus carpio (EL) 0 2.94(3) 0 1.95(3) 0 .0 0 5.23(7) 0 3.00(3) 1.31(16) Catostomidae (EL) 0 0 0 0.65(1). 0 0 0 0 0 0 Horone chrysops (YL)' 0.08(1) O O 0 0 0 0 0.68(1) 0 0 Etheostoma sp.~(YL) 1.00(1) 0.17(2) 0 0 0 1.30(2) '0 0 0 2.24(3) 0 0 0.42(51 Etheostoma sp.'(EL) O P 0 0 0.92(1) 0 0 0 0 Aplodinotus grunniens (YL) 0 0 0.04(1) 0 0 0 0 2.61(3) 0 e.75(1) 0 0 .0.3)(ej g lodinotus grunniens (EL) 0 .0 0 0 0 0.87(11- 0 0 0 0 0. 0g (1) Total Station Density 29.68(32) 50,05(51) 6.46(10) 16.92t26) s.31(9) 44.43(511 11.60(17) 38.09(51) 16.31(13) 43.96(44) 25.30(304) (number collected)
s
~ . + ; -
t #
.+ j. -
, , , ;y v TABLE V-H-1)
~(Continued)-
Total Date' Station l' ' Station 2 Station 3 ' Station 4 Station 5 . Collected and.
- g. l Night :g- ; Night. g Night :- g Night g Night Taxa @ensity
~
~
' June'13 .
a f th:1. water filhered (m )3 D 85.5 100.3 ' 69.5 ' 104.0 76.9 436.2 Kumber eggs collected 0 .'0' O 2 0: 2
-Number. larvae collected 2 2 1 -24 0 29 :
Number' juveniles collected 0- 1- ~0 3 3 0 -4. Number adults collected- 0- 0. ~0 0 0 ' f0 Density (number' collected) . Eggs.. Aplodinotus grannient 0-
'5.
1.arvae
'_ 0 0 1.92(2) 0 0.46(2)' :$
.Dorosoma cepedianum (EL). 0 1.99(2) ' 1.44 (1) 22.12(23) 0- 5.96(261 DU Notropis sp. (EL) 2.34(2) :0 0 0 0' ' O.4 6(2) - E$ .i
{ .' Aplodinotus gedaniens (EL) Juveniles 0
- 0. O
- 0.96 (1) . D '. 0.23 (1) :
c%, j en Dorosome cepedianum '0 - 1.00(13- 0' O.96(1) 0 ~ 0.46(21 g @ .. . ; Aplodinotus grunniens -0 0 0 1.92(2) 0 -- 0.46(2) 2 - Total StatiE Density h[. s (number collected) 2.34(2) :2.99(3)' 1.44(1) 27.88(29) . S 8.02(35)' *e 0 - t W G July 24/25 'Q & '
*E -
.Q O '! a vol. water filtered (m )
3 80,9 76.3 :102.4 108.1 85.7 86.3 107.6 80.9 81.8 70.0' 380.0 *1 k cumber eggs collected 1 0 8: 11 0 0 37 2 20 0 0 79 .'$ Z$
' Number larvae collected 'l 0 1 0 0 0 '0 2 .0 4<
- NumDer juveniles collected
' Eumber adua.ts collected O'
0 O 0 'O O 4 1 0 0 0 0 0 0
~5 0
0 0-0 0 9. 1-
'O i
Density (number collected) . Eggs . Aploiinotus grunniens 1.24(1) 0 7.81(8) 0 0 C l'. 86 (2) 1.24(1) O. 0 '1.36(12) . Unidentified eggs 0 0 0 10.18(11) 0 42.47(37! s 23.49(19) 0 'O 7.61(67)' , Larvae Pimephales sp. O P 0 0 0. 0 0 0 1.22(1)' O. 'O.11(1) Lepomis sp. (EL) 1.24(1) 0 ~0.98(1) 0 0 0- 0 0 1.22(1) 0 0.34(3) Juveniles Dorosoma cepedianum 0 0 0 0.93(1) 0 0 0 .1.24 (1) 0 0- 0.~ 23 (2) r.ctropis sp. 0 0 0 2.78(3) 0 0 .0. 3.71(3) 0 0 0.68(6). Percina sp. 'O 0 0 0 0 0- 0 1.24(1) 0 0 0.11(1) Adults . . Pereine caprodes 0 0 'O 0.93(1) 0 0 0 0' 0 0- 0.11(1) Total Station Density '2.47(2) 8.79(9) 14.80(16) 0 42.87(37). 1.e6/2) 30.90(25) 2.44(2) 0 .10.57(93) _..___.______..__________'__._.___ m._ _ -_ ^ - 2 ew ,, _ v _ * % --_
- , ,. . ;-W L- SR ,
~
. _y-- ,'_. _-
;.3 a n w.
-s %
g ,
-TABLE V-.H.1' (Continued)l '
=- "
Date' ' Station 1 Station 2' 1 Total 1 Station 3- Station 4 Station'5 ! y g :. Night'- :g: . Night -g. . Night
.g i Night jg
- Collected and4
. Night'-Tama Density' "
August'16 vol. water f11 tared3(a3 )'- 109.8 . 151.9 ' '122.6L 131.1- 105.0
~Eumber eggs collected 5- 9
'620.4
'l' 5 4, ' L 24 , '
Number larvne collected . 0 : 0: ,- 0.- 0
~
s 0 : 0- Q
;Kumber juveniles collected 0;
~
LO- -0 0 '0'
.Eneber adults collected 0
. 0:
- 0 .0 0-0 'O' Density.(number collected)..
' Eggs- _
Aplodinotus grunniens w'- 4.55(5) 5.92(9)' O.82(1) . 3.81( 5) . 3.81(4) Tc.tal station Density 4.55(5) 5.92(*)< 0.82(1) . ~3.81(5) -3.81(4)', 3.87(24)- $- _
'(number collected) .
3.87(24)-
~
_~-M ;
?
Year 3y Total
*O' 3
CC' Li
- > tu ' -
Vol. water tiltered'(m )- 508.7 178.2- 646.3- 261,' 501.4 201.1 - 617.0 a4.8 $
' Number eggs collected' +38 29 '
4 50.7 170.1- 3.7 50.1.; I
~ 21 ' . 2h '4 . 70 11 44 13 >1-Number larvae collected 7 22 260 ' g 291 8 7 18 40 27 6- 43 'H cumber juveniles' collected. 0 0 1: 4 0 '0= 3 188 I-X ~*
t* . 5 0 ~0- 13
-$ 2 Number adults collected 0 0 0: 1 0 0 0 0 0 0 1 Eggs Aplodinotus grunniens .l.Itf(6) 112.91(23) ' 2. 63 (17) ., ,5.35(14) 0.20(1) . 8.95(18) 1.46(9) 10.71(23)
' g *i ' ,
0.89(4) 0.59(1) 'J. 09 (116 ) . rc 'O r Unidentified egg 6.29(32) 3.37(6) 0.62(4) ,5.73(15) 0.60(3) '25.86(52) 0.32(2) 9.78(21) 2.00(9) 0 Larvae 3.84(144) ;$ y , Dorosoma cepedianum (YL) ? > *e , 0 0' '0- 0.38(1) 0 0 0 ' 0- 0. 0.59(13 C.05(2) Dorosome cepedianum (EL) O' 0 0.46(3) 0 0. 20 (1) - D.99 (2) . ~4.38(27) 4.66(10)- 0
.[$.
cyprinidae (YL) 0 0 -- *) '
- 2. 3 5 ( 4 ) .. 1.25(47) . p O 0 C.50(1) 0 0 0 0 ,0.03(1);
Cyprinidae (EL) . 0 8.42(15}- 0.15(1) 0.38(1) 0.43(23-
~.,
Cyprinus carpio (YL)
. 1.49(31 - 0.65(4) 1.40(3) 0.67(as 19.99(34)' 1.76(66) O.
0 2.24(4) '0.62(4). 'O 0. 60 (3) " '3.98(81' O.97(6) cyprinus carpio fEL) 0 1.68(3)
,1.40(3) 0.22(1) 'O. .0.77(29). .%,.
0 1.15(3) 0 0 .0 3.26(7). 0
. '1.76 (3) ~ 0.43(16)
Notropis sp. (EL) 0.39(2) 0 0J 0 0 ^0 0 0 a: Pinephales sp. 0 0 0 0 0.05t2) '
- 0. O' 0 0 0 ' O.22(1) . 'O Catostocidae (EL) 0 0.03(1)'
0 0 0.38(1)- 0 '0 0 0 0 0.03(1) Morone chrysops ' (YL) 0 0 0- 0 ' 0 'O
.- 0 '}
0.16(1) 0 0 0.59(1) 0.05(2)' Leposis,,sp. (EL) 0.20(1) O 0.15(1) ' O O 0 0
+
Etneostoma sp. (YL) 0 0 C 0.22(1) 0 0.08(3) 0 0.16(2) 0 0 0 1.40(31- 0 0 0.13 ( 5) -
'Etneostoma sp. (EL) 0 0 t' , 0 0.ft (1T 0
' C 0 0 0 Stirostedion'sp. (YL) 0.79(4) 0 0.15(1) 0 0 0.03(1) i Aplodinotus grunniens. (YL) 0 0.16(1) 0 0 0 0.16(6) 0 0 0 0 Aplodinotus grunniens (tL) 0' '1.49(3) 0 0.47(11 0 .0 0.11(4) 0 0- 1 0 0- 0.50(1) 0.16(1) 0 0 0.0 5(2) .
'O
]
f e
. . . .. , _ ~ -
TABLE V-H-1 (Continued) i Total Stadon 2_ Station 3 Station 4 Station _$ _ Collected and Date Station 1 g Night g Might Taxa Density.. g Nignt M Night. , M $$ Y vrly Total-(continuedi Juveniles 0 0.16(1) 0.47(1) 0 0 0.11(4) 0 0 0.15(1) 0.38(1) 0 0.16(6) _Dorosoma cepedianum 0 n.15(3) 0 0 0 1.40(3! O O 0 0 0 0.03(1) Yberopis sp. 0 ft 0 0 0 0.47(1) 0 M Pereina sp. 0 0 0 0.72(2i J 0 0 0.05(2) Aplodinotus grunalens 0 0 0 0 C h Adults 0 0 0 0 0 0.03(1)' 0 0.38(1) 0 Perciata esprodes Total Station Density 0 0 8.85(45) 28.62(51) 4.95(32) 16.04(423' 2.19(11) 43.7Et88) 8.75(541 35.38(76) 4.22(19) 25.87(44) 12.32(462) ge g-(number collected) CC i yQ l Developmental Stages Z g to l YL - Ratched specimens with yolk and/or oil globules present, < p s-g EL -- Speciserr, with no yolk and/or oil globules and with no development of fin rays and/or spiny eierents. Nb p M 84 : x QO
-> S -
. >m ! C* . w .< _ to
*ts -
O k e l
- - _ _ _ h
DUQUESNE LIGilT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT Spatial Disttjbution TP 1991; totals for number of eggs and number of larvae were comparable a, j '.g the five stations surveyed. The least number of eggs (14) were collected - at ' Station S.- The most larvae (67) were collected at Station 4. .Most of the larvan collected in 1991 were . gizzard shad, unidentified cyprinids, and carp. S tations 1,_ 2, , 3, 4, and 5 yielded 29,-18, 25, 67, and 49 larvae, respectively for 1991. -! i Summary and conclus'.ons 7 The 2najority of the ichtnyoplankton collected in 1991 were egg s and larvae, which comprised 56.3% and 40.7% of the total catch, respec-ti vely.~ Juvenile and adult fishes for the remaining 3.0% of the catch. The similarity of species _ composition and relative abundance of ichthyo-plankton taken in 1991 along the _ river transect to those of 1979-1990, c6mbined with the close correlation between river sampling ir. f ront of -
.the intake and actual entrainment sampling established in previous years (DLC 1976,1977,1978 and 1979) suggest little change in ichthyoplankten - entrainment by BVPS in 1991.
- 2. Phytoplankton Objectives The phytoplankton entraintment study was designed to determine the compo-sit. ion and' abundance of phytoplankton entrained in the intake water sys-tem.
Methods After. April 1, 1980, plankton sampling _ was reduced to one entrainment sample collected . monthly. A one gallon sample was collected f rom below the skimmer wall from one operating intake bay. 118
DUQUESHE LIGHT COMPANY 1991 ANNUAL ENVIRO 1 MENTAL REPORT In the laboratory, phytoplankton analyses were per formed in accordance with procedures described in Section C, PHYTOPLANKTCH. Total densities (cells /ml) were calculated for all taxa. However, only densities of the 15 most abundant taxa each month are presented in Section C of this report. Comparison of Entrainment and ' liver Samples g- Plankton samples were not collected at any river stations after April 1, 1980 duo to a reduction of the Aquatic Monitoring Program, therefore, comparison of entrainment and river samples was not possible for the I 1991 phytoplankton program. Results of phytoplankton analyses for the entrainment sample collected monthly are presented in Section C, PHYTOPLANKTCN. During the years 1976 throught 1979, phytoplankton densities of entrain-ment samples were usually slightly lover than those of mean total densi-ties observed f rom river samples (DLC 1980) . However, the species com-position of phytoplankton in the river and in the entrainment samples were similar (DLC 1976, 1977, 1979, and 1980). S tudies from previous years indicate mean Shannon-Weiner indices, evenness and richness values of entrainment samples were very similar to the river samples (DLC 197 9, and 1980). Summary and conclusions Past results of monthly sampling of phytoplankton in the Ohio River near BVPS and within the intake structure showel lictie dif f erence in densi-ti es (cells /ml) and species composition. During periods of minimum low river flow, approximately 5% of the river would be withdrawn into the condenser cooling system. Based on the similar densities of phytoplank-ton in the river and the BVPS intake structure, and the small amount of water withdrawn from the river, the loss of phytoplankton was extremely small even under worst case low flow conditions. 119
DUQUESNE LIGitT COMPAMY 1991 MINUAL ENVIRONMENTAL REPORT
- 3. Zooplankton Objectives The zooplankton entrainment studies were designed to determine- the com-position and abundance of zooplankton entrained in the intake water sys-tem.
-Methods Plankton entrainment samples were collected and zooplankton were counted. For the zooplankton analyses, a well-mixed sample was taken and procissed using' the same procedures described in Section D,- ZOOPLANKTQ1.
After April 1, 1980, plankton sampling was reduced to one entrainment sample collected monthly. A one gallon sample was collected f rom below the skimmer wall f rom one operating intake bay. Total densities (number / liter ) were calculated for ' all ta xa , however, only taxa which ccznptised greater than 2% of the total are presented in l' Section D, ZOOPLANKTON. L Con.parison of Entrainment and River Samples Plankton samples were not collected at any river stations af tet April 1, 1980 due to a reduction of - the Aquatic Monitoring - Program, therefore, comparison- of entrainment and river samples was not possible for the 1991 zooplankton program. Results of zooplankton analyses for the entrainment sample collected monthly are presented in Section D, 200-PLANKTOI . During past years, composition of zooplankton was similar in entrainment and river samples (DLC 1980) . Protozoans and rotifiers were predomin-ant, whereas crustaceans . were sparse. _ Densities of the four most abun-dant taxa for each month (DLC, 1976, 1977, 1979, and 1980) indicate the same taxe were present_in both river and intake samples. In addition, 120
DUQUESNE LIGHT COMPANY , 1991- ANNUAL' ENVIRONMENTAL REPORT - l l they were present' in'similar quantities. Shannon-Weiner indices, even-ness, and richness values for river and entrainment samples were also similar, further demonstrating similari ty between entrained and river r% plankton. Summary and Conclusions l Past results of monthly sampling of zooplankton in the Ohio River near
- BVPS and within the intake structure showed little diff erence in densi-ties (number / liter) and species corrposition. During periods of minimum, j low river flow, approximately 51-of the river would be withdrawn into the condenser cooling system. Based on the similar densities of zoo-plankton in the river and the BVPS intake structure, and the small amount of water withdrawn from the river, the loss of zooplankton was extremely small even under worst case low flow conditions. ,
4
- 1. Corbicula MONITORING PROGRAM
' Introduction The introduced Asiatic clam, Corbicula fluminea (Figure V-I-1), was first detected in the United States in 1938 in the Columbia River near Knappton, Washington (Burch 1944). It has since spread throughout the country, inhabiting any suitable freshwater habitat. Information from prior aquatic surveys has demonstrated the presence of Corbicula in the Ohio "1ver in the vicinity of the BVPS, and the plant is listed in
. NUREG/CR-4233 (Counts 1985) .
One- adult clam is capable of producing many thousands of larvae called veligers. These veligers are very small (approximately 0.2 mm) and will pass easily through the water passages of a power plant. Once the veli-ger settles to the substr ate, growth of the clam occurs rapidly. If
- clams - develop ' within a power plant's water passages, they impair ' the flow of water through the plant. Reduction of flow may be so severe that a plant shutdown is - neces sary, as occurred in 1980 at Arkansaa Nuclear One Power Plant. The clams are of particular concern when they 121
. _ _ _ _ _ . . . _ _ _ _ . . _ . ~ . . _ _ _ _ _ _ _ _ _ _ _ - - _ . _ . . _ _ _ _ _ - _ _ _ _ - _ _ . _ . _ _ _ . _ .
1 i: DUQUESNE LIGHT COMPANY l ANNUAL ENVIRONMENTAL REPORT Asiatic Clam Zebra Mussel ADULT ADULT ( m, .::, . 7 6 .
, %~ $
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l Corbicula LARVAL CAGE NOT TO ZEBRA MUSSEL SCALE ARTIFICIAL SUBSTRATE FIGURE V-I-l PHOTOGRAPHS OF Corbicula WITH LARVAL CAGE AND ZEBRA MUSSEL WITH ARTIFICIAL SUBSTRATE BVPS
DUQUCSNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT develop undetected --in. emergency systems where the flow of water is not constant- (NRC, IE Bulletin 81-03). Tha Corbicula Monitoring Program includes the Ohio River and the circu-lacing- river water system of the BVPS (intake structure and cooling towers). This report describes this Monitoring Program and the results obtained during . field and plant surveys conducted through 1991. 1 -. Monitoring objectives The two objectives of the Monitoring Program were to evaluate the pres-ence of Corbicula at the BVPS and to assess the population of Corbicula in the Ohio River in order to evaluate the potential for infestation of the BVPS.
.M3thods (Unit 1 Cooling Tower)
The Corbicula population in the lower reservoir of the (Mit 1 cooling tower was es timated b'a sed on sampling performed during a scheduled outage. Seventeen samples were collected on April 18, 1991 at desig-nated sampling locations using a (6" x 6") petite ponar dredge (Figure V-I-2) . The substrate of each sample was characterized at the time of collec-tion. The samples were returned to the laboratory and sorted for
- Corbicula within 72 hours of collection. This procedure increased over-
. all sor ting efficiency because formalin, normally used to preserve the
-samples for long periods of time, was not needed and live Corbicula i could be. seen moving in the sorting trays. Counts were made of live and dead Corbicula in each dredge sample. These sample counts were con-2 verted to densities (clams /m ) based on the surf ace area sampled by the dredge. An average density was then calculated for the seventeen 123
DUQVESNE.LIGilT COMPANY 1991 AttNUAL ENVIRONMENTAL REPORT i-i i ('IVO DIMENSIONAL:- CROSS SECTIONAL HORIZONAL VIEW) N + " '
%d
) 12 -
11 # l 9 e 10 13 S T AIR WAY e e2 97 99 16 9 17 9 9 14 93 { i S TAIRWAY x
~
e* a 4 M 7' . 6 s
' WAT E'R ' . OUTLET- '
t _ EQUIPMENT - I- . . ACCESS RAMP 50 FEET 0: SAMPLE LOCATION' WITHIN -THE LOWER WATER RESERVOIR FIGURE V-I-2 Corbicula MONITORING PROGRAM SAMPLING STATIONS OF Tile-LOWER RESERVOIR OF UtiIT 1 COOLING TOWER BVPS 124
DUQUESNE LIGHT COMPANY 1991 ANNUAb ENVIRONMENTAL REPORT samples. An estimate of the area of the cooling tower basin covered by sediment was calculated, since the ,Corbicula were concentrated almost entirely in the sediment. The estimated population was calculated by multiplying the average density times the area of sediment coverage. (Intake) Plant operations personnel have the intake surveyed semi-annually by divers for silt buildup, and if necessary, the intake bays are cleaned. Cleaning of intake bays occurred in April and October 1991, by divers using a Flygt 20-hp submersible pump. This pump has a capacity of 500 gpm (1,750 rpn) and uses a five-inch propeller to push water and debris through a flexible hose (Jenkins and Logar 1985). Water and debris were sluiced through the drainage system of the intake structure, where some
. of the larger clam shells remained af ter the cleaning operations.
(River) Surveys were performed in May and September of 1991 to monitor for Corbicula in the Ohio River near the BVPr Ten transects were estab-
- lished along the Ohio River s four upstream, five downstream and one at the plant intake (Figure V-I-3) . A transect was al so established on Raccoon Creek. Two transects downstream of the BVPS (Phillis Island and Georgetown Island) were divided, resulting in samples being collected on both sides of each - island. Each transect was established on suitable substrata (sand and/or gravel) or near a heated discharge (HD). Each transect is identified by river navigation mile on Figure V-I-3. Thir-teen additional samples were collected near the left bank next to the BVPS (Figure V-I-4). These samples were concentrated mainly in front of the intake structure.
Samples were collected using either a regular ponar (9" x 9"), (r egular benthic program, transects 1, 2A, 2B and 3) or a petite ponar (6" x 6") dredge. Three sampics were collected at each transect (left shore, right shore and mid-channel), except for benthic transects 1 2A and 3 which included a duplicate lef t sample as part of the benthic program. I 12,5 '
i 8EAVER RIVER N ROCHESTER 28.2 DEAVER ) , 30.0 CONWAY YN 33.0 37.0 s OHIOVIEw g y 0.2 -
- y. RACCOON \ $@
\
C#EE# \ bO k MIDLAND P MotuunERY s g yg g, LOCKS & DAM j z GEORG" M Q C -6 BEAVER 34.5 jf *b
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/al VALLEY ALIQUIPPA f j PWER j @o
< STATIW j(
35.7 ! AMBRIDGE c' t 35.4 l 4 34.8 0 ! 2 4 35.0 SCALE MILES LEGEND south
>--4 SAMPLE STATION RIVER MILE POINT I I
DASHIELDS LOCK & DAM FIGURE V-I-3 Corbicula MONITORING PROGRAM SAMPLING STATIONS, 01110 RIVER SYSTEM BVPS I
DUQUESNE LIG11T COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT
; l
~ BARGE SLIP
- l. 1A l l'
Y ' UNIT 1 COOLING TOWER 2A i l 3A 8 A 4A 6A -A INTAKE-7 A 10A STRUCTURE 5A lle 4 1 12 A SYMBOLS 13 g SAMPLE LOCATION RIVER FLOW i i ! FIGURE V-1-4 l Corbicula MONITORING PROGRAM SAMPLING STATIONS, OHIO RIVER SYSTEM l IN THE VICINITY OF THE INTAKE STRUCTURE BVPS l l \
~
127 l_
DUQUESNE LIGIIT-COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT
'.The: substrate of each - sample was characterized at the time of collec-tion. The samples were _ then returned to the laboratory and sorted for Corbicula. Counts were made of live and dead Corbicula- for each dredge sample. 2 I.l ve clam counts were converted to densities (clams /m ) for each sample based on t..a surf ace area sampled by the dredge.
The weekly impingement ' surveys at the intake structure monit:;ed the number of Corbicula which could potentially enter the BVPS from the Ohio River. Corbicula obtained during the washing of the traveling screens (see Section G, Fish Impingement Methods), were returned to the labora-tory. These clams were rinsed through a series of stacked U. S. stan-
'dard sieves ranging in mesh-size from 16.0 mm to 0.6 mm. The number of live clams retained on each sieve was recorded.
Results
- (Uni t 1 Cooling Tower ) -
Results of the April _18, 1991 Corbicula survey of the Unit 1 cooling tower are presented . in Table V-I-1. Only two of the 4,670 Corbicula collected in the 17 samples were alive. Based on the seventeen ponar samples taken from the lower reservoir, the es tima ted number of Corbicula inhabiting ' this area was 160.0 million, of which 99.9% -were dead - (Figure V-I-5) . In 1990, DLC initiated a corbicula Control- Program which included the use of a molluscicide (CT- 1) to help prevent the prolif era tion of Corbicula within the BVPS plant and cooling _ towers. DLC was granted permission by the Pennsylvania Department of Environmental Resources to use this molluscicide in-the BVPS river water systems. The ini tial CT-1
' dosing.' of Unit I was performed' on June 20 and 21, 1990 and the 'second dosing was on November 20 and 21,1990. Corbicula which had entered the Unit 1 cooling tower basin since the previous (scheduled) outage of i S epte.nber 1989 were killed by the ini tial molluscicide ' application.
Corbicula which entered the Unit 1 cooling tower subsequent to the June dosing were killed by the November dos i ng . A recolonization of the 128
DUQUESNE LIGilT COMPAf4Y 1991 AtlNUAL Cl4VIROllMENTAL REPORT TABLE V-1-1 Corbicula COLLECTED IN UNIT 1 COOLING TOWER I APRIL 18, 1991 DVPS Clams Collected StationDensigy Sample Location Substrate Alive Dead Live Clams /m Upper Reservoir Qualitative Sample sil 0 20 0
# East) i Lower Reservoir 1 all 0 560 -
0 2 all 0 564 0 3 si) 0 128 0 4 sil 0 44? O 5 sil 0 '56 0 6 sil 1 293 43 7 sil 0 272 0 8 sil 0 106 0 9 sil 0 11 0 10 sil 0 J23 0 11 si) 0 558 0 12 sil 1 455 43 13 sil 0 135 0 14 sil 0 11 0 15 sil 0 137 0 16 sil 0 3 0 F sil 0 13 0 Substrate Codes: sil - silt 9 129
m mwn vPucATNsF 350 ' (1.7%) 300' 300 - c n~- - ~ 260 -
~
200 - 8%) '~~ 178 c (99.9%)* 160 - 150 - o e
~
~ iE 8 .
zo 100 - Ilf8%I~ '
~~ ~
l~ ~ EE i E 70 E* _ p (46.5%) v 14.4%)_ L58.3%)_, 5 E-
=9
' 60 i 30 34 i
' 20 18.5 5o o
i l'j O g] h$ 0 .7,iii ' ~ ' - -- iiiis'c.
' ' ~ ' - ' - '
e- >
- i. ii..i . iiis'iii i,.i,iT , , i i '. :
iii . iiiiiei ,,,ii6 . TT4 - 6 6 g MJJASOND 88 JFMAMJJA80ND JFMAMJJASOND JFMAMJJASOND JFMAMJJASOND JFMAMJJA80ND g 87 88 89 90 91 g
- UNIT 1 M unit 2.
Survey performed after 1990 Corbicula Control Program, June and November 1990 molluscicide dosings of Unit I river water system. ( ) Indicates percentage of dead Corbicula in the estimated total. FIGURE V-I-5 APPROXIMATE POPULATIONS OF-Corbicula IN UNITS 1 AND 2 COOLING TOWERS DERIVED FROM SURVEYS CONDUCTED IN 1986 THROUGH 1991 BVPS
--w ,., m
. - . - - ..- . .- - - ~ - -
. - - .- -c_. .
DUQUt:SNE LICllT COMPAISY 1991 ANNUAL ENVIRONMENTAb REPORT Unit l' cooling tower following the November 1990 dosing apparently did
.not occur as supported by the 99.9% corbicula mortality in the popula-tion survey samples and the absence of Corbicula in the larval cage _
removed (Ap il 15, 1990) frcan the Unit 1 cooling tower prior to the outage (Table V-1-10, Corbicula Larvae Study Section) . (Intake) While perforring the innettay cleaning operation (April and October 1991), the divers observed concentrations of Corbicula in each of che bays close to the intake pumps. As in past years, mort lams were a tmoved during the autumn cleaning operation than in the spring cleaning operation. A cut-away diagram of the !itake structure id provided in . Figure V-I-6. (River) The results of the 1991 Corbicula surveys in the Ohio River are pre-sented in Tables V-I-2 and V-I-3 (May) and V-I-4 and V-I-5 (September ) . - Dead.C6tbicula were not countad in samples of the regular 1 benthic macroinvertebrate monitoring program. Live Corbicula were collected primarily in substrates composed of silt, sand, and/or gravel. Substantially fewer live Corbicula, were collected in May (27 in '5 samples) as compared to the September survey (287 in 55 samples). Live , 2 Corbicula, densi ties e xceeded 100/m for twenty-two of the September 2 samples. The highest density of 776 ' clams /m -(September) occurred at mile 34.5 (Transect 1) of the Ohio River, upstream f rom the BVPS. A 2 comparable density (768 clams /m ) was calculated for a sa'ople collected at river mile 35.4, downstream f rom the BVPS. Table V-I-6 summarizes Corbicula dend ties in past macroinvertebrate collections for the BVPS ' (1973 through 1991). No Corbicula were found at any sampling station during 1973, 1979 and 1980. Corbicula densities were generally higher in the f all *.han in the spring surveys. l 131
DUQUCStic LIGitT COMJAt4Y j 1991 Atit10AL EtNIRotiMEllTAL REPOKl' l l i ( T HREE DIMEfisl0N AL : CUT AWAY VIEW) o - 1 t i TRASH Y l' . 961
^
7 ARE A CLEANE D BY
- OlVING OPERATIONS w
- ,h '1 -
4 p- - TR AVELING SCR E E N aN r D
- I I
AD " C i B I& %, m ,~ 3
~~~ ~
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BAY - ARE A CL E AtlE D BY DIVlHO OPERA TlONS BAY D (TWO DIMENSIOflAL: SIDE VIEW) [a 4 7 g [ TRAV El.lNO SCRE EN
/ TRASH RACK ARE A CLE ANED BY Dl'/ING OPER ATION S p 1
/
w bhj hd
//
. /
ARE A CLE ANED BY DIVING OPERATIONS FIGURE V-I-6 ? Corbicula MONITORING PROGRAM SAMPLING STATIONS - INTAKE STRUCTURE BVPS 132
DUQUESHE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT i TABLE V-I-2 ! Corbicula COLLECTED 3N THE OHIO RIVER MAY 13 AND 14, 1991 BVPS Class Station S ample River Collected Density Location Mile Bank Depth (ft.) Substrate Alive Dead Live Clams /m 2 Raccoon Creek 0.3 R- 4 sil 0 0 0 M 4 sil/ san 0 0 0 - L 2 sil 0 0 0 Ohio River 24.2 R 2 sil/ san 0 0 0 M 33 3ra 1 0 43 L 1 mil 0 0 0 30x0 R 2 s!! 0 1 0 M 36 san /gra 0 1 0 L 2 cob 0 0 0 1 33.0 R 4 cla/sil 1 0 43 , M 21 gra 0 2 0 L L 2 all 0 3 0 34.5(II- R 3 sil/ san 3 3 129 M 22 cob 0 0 0 E L 3 sil 1 - 20 L 3 sil 2 - 39 34.8 R 3 all 0 5 0 M 20 bed 0 0 0 L 23 sil 1 2 43 (Back Channel) 35.0 R 4 sil/ san /det 0 10 0 M 24 san /gra 3 6 129 4 sil 0 0 0 35.4(2A) R L(HD) 4 cob 0 0 0 M 18 san /gra 0 2 0 L 3 sil/ san 2 - 39 L 3 sil/ san 0 - 0 (Back Cbc.nnal) 35.4(2B) R 3 sil 2 - 39 M 11 gra 0 - 0 L 2 mit 2 - 39 (Back Channel) 33.7 R 3 sil/aan 0 2 0 M 12 gra 0 0 D L 3 cla/sil 0 3 0 37.0 I3I R(HD) 2 sil 0 2 0 M 29 gra 0 0 0 L 3 sil 1 - 20 L 2 s11 1 - 20 - 37.5 R 5 sil/ san .0 0 0 M 22 gra 0 4 0 L 4 sil 0 2 0 (Back Channel) 37.5 R 4 sil 0 0 0 M 15 sil/ san 0 4 0 L 3 all 0 4 0 Scbstrate Codes: Footnotesa bed - bedrock. (HD) - 11eated Discharge cla - clay. (1) - Transect 1 r . cob - cobble (2A) - Transect 2A (Main Channel)
- det - detritus (2D) - Tr ansect 2D (Back Channel) gra - gravel (3) - Transect 3 san . sand i sil - sitt 133 !
=1
, ~ . _ . . - . - - m.,.
DUQUESNE LIGitT COMPANY 1991 /d4NUAL ENVIR0llMENTAL REPORT TADLE V-I-3 Corbicula COLLECTED IN Ti!E Orio RIVER Ill THE VICINITY OF THE INTAKE STRUCTURE t%Y 13, 1991 DVPS Class Station Sample Collected Density , g ation Depth (f t. ) Substrate Alive Dead Live Clams /m 2 j
-(Left bank) i 1 4- gra 0 1 0-
'2 4 gra. 0 3 0 3 3 .gra. 0 0 0 4.,
19- sil/ san /gra 0 9 0 19 . san /gra 2 16 86 6= 21 sil 2 5 86
.- 7 22 sil/det 2 13 06 ,
8- - - 22 sil 0 , 3 , 0 9 22 sil. 0 . 7 'O 10 ~ 22. -sil 0 3 0 11 21 sil 0 10 0 12 2 sil- 0 5 0 13 2 sil 1 1 43 Substrate Codes:- *
~ cob - cobble det'- detritus gra.- gravel--
san - sand all - silt i e Y
~134 T +8 4g- g- FW" *T--
.DUQUESNE LIGitT COMPA!1Y 1991 ANNUAL ENVIRONMENTAL REPORT l TABLE V-!-4 P
Corbicula COLLECTED Ill THE OHIO RIVER SEPTEMBER 30, 1991 DVPS E Class Station Sample River Collected Density 2 Location Mlle Bank Depth (ft.) Substrate Alive Dead ' Live Clams /m { Raccoon Creek 0.3 R 5 sil 0 0 0 M $ s11 0 0 0 l L 2 sil 3 0 0 Ohio RivJr 28.2 R 2 mil 0 1 0 M 31 bed 9 1 0 L 1 nil / san /det 3 1 129 30.0 R 2 sil 1 0 43 M 36 san /gra 0 1 1 L 3 sil/ san /gra 6 1 259 33.0 R 4 sil/det 2 8 86 M 21 san /gra 16 11 690 l L 1 sil/ san 3 2 129 i 34.5III R 2 sil/ san. 10 8 431 l .H 23 gra/ cob ' 18 11 776 L 3 sil 20 - 394 L 2 all 9 - 158 34.8- R 3 sil/ nan 8 1 345 M 21 san /gra 1 2 43 L 22 sil/ san /det 6 16 259 (Back Channel)- 35.0 R 3 sil/ean 0 1 0 23 sil/ san 1 7 43 M(nD) L 1 sil 0 1 0 3!.4I2AI- R 4 gra 1 0 43 M 17 san /gra 9 4 388 L 3 cla/ san 19 - 374 L 2 cla/ san 39 - 768 (Back Channel) 35.4(26) R 2 s!1 26 - $12 M- 12- san /gra/ cob 2 - 39 L 3 all '1 - 138
.(Back Channel) 35.7 R 2 sil 3 15 59 M 12 gra/ cob 1 5 20 L 3 s11 4 29 79 'i
'37.0I3I R(HD) 2 s!! 4 1 172 M 20 gra/ cob. 0 2 0 ,
L 3- -nil 5 - 99 L 2 sil 6 - 118 37.5 R 2 cla/sil/gra 0 1 0 M 23 gra/ cob 1 1 43 L 4 sti 2 5 J6 e (Back Channel) 37.5 R 2 mil / san- 2 4 86 M 14 sil/ san 2 3 86 , L 4 sil/ san 7 5 302 l? Substrate Codes: Footnotes bed - bedrock (Ha) - Heated Discharge
.cla clay (1) - Transect )
cob - cobblei (2A) - Transect 2A (Main Channel) det - detritua (20) - Transect 2D (Back Channell l gra - gravel (3) - Transect 3 I san - sand l sil - silt 13,5 l
- l. ,
( i. DUQUESNE LIGili COMPAt1Y - 1991 IJiNUAL ENVIRONMENTAL REPORT TABLE V-I-5 Corbicula COLLECTED 114 Tile 01110 RIVER IN T!!E VICINITY OF Tile INTAKE STRUCTURE SEPTEMBER 30, 1991 DVPS Clams Station Sample Collected Density . Location Depth (ft.) Substrate Alive Dead Live Clams /m" (Left bank) 1 5 sil/ san /gra 11 2 474 2 4 g ra/t.ob 0 0 0 3 4 g ra/cc.b _ 2 0 86 4 18 sil/ san /gra 1 3 . 43
. 5 12 gra 7 2 302 6 21 sil/det 0 4 0 '
7 22 sil/gra 1 11 43
.8 22- sil/det 3 4 129 9 23 sil/det 2 8 86 10 23 sil/det 1 20 43 .
11 20 mil /det 1 24 43 12 4 sil 2 5 86 _13 _17 sil 13 29 560 _ Substrate Codes:- cob --cobble det - detritus gra:- grave 1~' , aan - sand sil - silt 136
,, m , v , .+--e_,e .-..
DUQUESNE L1 Gilt COMPANY 1991 ANNUAL EIN!RONMENTAL REPORT TABLE V-I-6 2 Corbicula DENSITIES (Clams /m ) SUMMARIZED FROM BENTHIC MACROI!NERTEBRATE COLLECTIONS
, 1973 Tila00Gli 1991 LVPS TRANSECT 1 2A 2B 3 Back Date L M R L M R Channel L M R 1973 Nov T 0 0 0 0 0 0 0 0 0 1974- Hay . 0 0 0 0 0 0 0 0 0 0 J ut. - 0 0 0 0 0 0 0 0 0 0 Jul 0 0 0 0 0 0 0 0 0 0 ,
Aug 0 0 0 0 0 0 w 0 0 0 Sep 0 0 7 0 0 0 0 0 0 0 1975 Aug 26 7 0 20 20 20 33 20 7 0 0 Nov 13 ( 0 0 7 46 0 7 0 198 0 1976 Feb 24 7 0 'O O O C 13 0 0 0 May 25 0. 0 0 0 0 0 0 0 0 0 Aug 18 40 20 290 99 0 53 92 0 20 0 Nov= 0 0 3b6 13 475 20 139 7 422 13 i' 1977 Feb 24 0 0 7 7 53 508 7 0 7 0 May 17 0 0 0 0 0 0 ( 0 0 0 7 86 172 0 Aug 17 0 0 0 0 7 13 0 Nov 13 20 59 0 46 13 46 7 145 0 197& Feb 15 0 13 0 0 0 132 6 6 6 32 May .18 0 0 0 0 0 0 0 0 0 0 Aug .* O O O 6 13 0 0 0 0 0 Ncv. 14&l5 25 13 0 6 403 38 32 6 19 6 1979 Mar 22 0 0 0 0 0 0 G *n 0 0 May 25 0 0 0 0 0 0 0 0 0 0 Aug 1 0 0 0 0 0 0 0 0 0 0 Nov 14 0 0 0 0 0 0- 0 0 0 0 1980 Feb 13 0 0 0 0 0 0 0 0 0 0 May 21 0 - - 0 - - 0 0 - - Sep 23 0 - - 0 - - 0 0 - - 1981 -May 12 0 - - 0 - - 7 0 - - Sep 22 40 - - 90 - - 408 99 - - 1982 May 18 0 - - 0 - - 0 0 - - Sep 23 0 -= - 10 - - 0 0 - - 1983 14ay 11 20 - - 0 - - 0 0 - - Sep 13 59 -- - 20 - - 251 40 - - 1984 Hay 10' 0 - - 0 - - 7 0 - - Sep . 6 0 - - 0 - - 0 0 - - 1985 May 15 0 - - 0 - - 0 0 - Sep 19 - 85 - - 0 - - 99 40 - - 1986 May 13 0 - - 0 - - 0 0 - - Sep 15616 20 - - 20 - - 184 0 - - 1987. Hay 13 0 - - 10 - - - 20 30 - - Sep 16617- 30- - - 118 - - 59 99 - - 1988 . Hay. 10 0 - - 49 - - 33 30 - - Sep 13 325 - - 118 - - 92 79 - -
--1989 May. 23 0 - - 0 - -
39 10 -
-Sep .14 20 - -
118 - - 197 108 - - 1990 May 465 0 -- - 0 - - 111 10 - - Sep .13 197 - -
'148 - 112 20 - -
1991 May. 13 30 - - 20 - - 79 20 - - Sep 30- 276 - - 571 - - 690 108 - -
.4
(-) indicates area not sampled 137
DUQUESHE LIGl!T COMPANY 1991 AtMUAL ENVIRONME!'fAL REPORT l l Table V-I-7 summar i ze.1 Corbicula densities (clams /100 m 3 volume water filtered) in ichthyoplankton samples collected monthly April through August for 1988 through 1991. he July 1991 night survey collected the most Corbicula in the four-year period. The highest density wr1 641.53/100 m, calculated for the July 25 (night) S ta tion 4 Bottom sample. Size distribution data for live Cor bicula collected f rom the traveling screens during the weekly impingement surveys in 1991 are presented in Table V-I-B (see Table V-G-7, Section G) . The majority of clams col-lected (48.2%) were retained on the 6.3 mm mesh size sieve. The largest number of Corbicula (113) were collected on July 26, which coincides - with the high densities of Corbicula found in the July (night) ichthyo-plankton samples. Young clams (sieve mesh sizes 3. 3 5 and 6. 3 mm) were consistently collected from July through mid-November, as were young adults (si eve 9.5 mm). Larger Corbicula (12.5 and 16.0 mm sieves) compr i s,s:u ..ly 4.1% of the impingement total. No juvenile cl'ams Kl.00 mm) were collected due to the large mesh size (1/4 ") of the impingement collection basket. The small peak which occurred on May 3, 1991 (65 live Corbicula) was due to the inner bay cleaniag operations by divnes, rather than a natural influx of Corbicula from the Ohio River. Table V-t-9 uses the size distribution data f rom Table V-I-8 and cc,a-verts it to a standard unit, which is the number of live Corbicula 2 collected /1000 m of traveling screen washed. This was Jone because the number of intake bays which were in operation was not always const ant f rom one week to the next. Figure V-I-7 presents the data from Table V-2-9 as an average for each month in 1991. Figure V-I-8 presents monthly totals for Corbicula collected dur ing impingement surveys for the years 1981 thrriugh 1991. The Corbicyla_ impingement data for 1991 was comparable to 1988 and 1990, however, che maximum rr.onthly total (309 in September) was the lowest since 1987. The I large peaks observed in 1989 (12,362 in September; 2,263 in October) did r.ot occur in 1991. 138
I. DUQUCSHE LIGIIT COMPANY 1991 ANNUAL DIVIRONMENTAL RCPOllT TABLE V-I-7 Corbicula del >SITIES (Clams /100 m ) 3PRESDIT IN ICitTHYOPLANKTON
, SAMPLES COLLECTED WITli A 0.5m PLANI. TON NET IN Tl!E 01110 RIVER, 1988 T!! ROUGH 1991 DVPS itasp,11 toea t i on Back Channel Main hennel Date T Sur ~ }B 'not~ [ Sur 2 Bot 3 Sur 4 Dot S sur 1998 April 10 0.62 8.96 0 0 0 0 0 May to 0 0 0 0 0 0 0 May ll I*I 21.87 18.9% 0 0.00 0 1.00 21.00
. fung 14 0 0 0 0 0 0 0
.luly 14 0.90 0 0 9.24 0 0 0
.foly 14I *I 0. 54 9.09 *0 14.75 0 17.06 3. 52 Aiegini t 17 0 0 0 1.60 0 2.70 2,06 1989 -
April 13 0 0 0 0 0 0 0 Mer 23 0 0 0 0 0 0 0 May 24I *I 0.78 6.40 2.00 0 0 0 2.64 Juna 19 0 0 0 0 0 0 0 Jesty.12 0 0 0 0 0 0 0 July 13 I*I 4.04 9.99 4.37 3.38 0 1,67 1.18 An1991 is 0 0 0 0 0 0 0 1II.S Artil le 0 0 0 0 0 0 0 May 24 0.79 0 0.88 0.70 0.70 0 0 May 25I *I 0.79 3.33 0 0 0 f.4 3 2.90
.1une 12 0 0 1.82 0 0 0 0 July 25 46.32 40.62 47.97 77.62 40.36 47.10 00.14 July 26I *I 38.40 26.01 51.65 30.42 15.44 14.52 375.4*
l Autost 21 1.01 0 1.71 1.95 0 3.70 0 1 tal Night sur vey was conclui.ted, i 1 i- 139
- TABLE V-I-7 (Continued) -g i
- Sample Location Back Channel Main Channel
} -. Date 2B Sur 2B Bot 1 Sur 2 Bot 3 Sur '4 Bot 5 Set 1991 e P.pril 19 0- 0 'I O O O O '0 May 13 -0 0 0 0 0 0 0 D8 Eo May 14I *I EE 14.29- -21.68 2.94 0.65 0 2.24 6.99 C' E D 02 H June 13 0 0
- 0 0 0 0 0 3 C' 4
o :e n ' g ::: July 24 .0 'O 0 .. 0 0 0 0 5 d E o-July 25 I8I 8.59 5.77 2.62 36.08 275.78 640.30 351.43 $ EE E August 16 0 0.60 0 0 0.82 0 0.95 5* o "I N!)ht survey was conducted. 1
i 'l- . in . 1 I,
,y SIZE DISTRIBUTION OF Corbicula COL DURING IMPINGEMENT SORVnS FOR ONE 24-HOUR PERI . WEEK, 1991 BVPF
~
Live Clam Size Distribution Numbers Total Date $1.00 (m:n) 3.35(mm) 6.3(mm) 9.5(mm) 12. 5 (m) 16.G(mm) Live Clams January 4(a) _ _ _ _ _ _ _ 11 0 0 0 0 C 0 0 18 0 0 0 0 0 0 0 25- 0 0 0 0 0 0 0 C February 1 0 0 0 0 0 0 $ 8 0 0 0 0 0 0 0 go 15 0 0 0 0 - 0 0 0 ES 22 0 0 0 - 0 0 0 0 SE rg - March 1 0 0 0 0 1 0 1 EC5 8 0 0 0 0 0 0 0 $C
, 15 0 0 0 0 0 0 0 $E - 22 0 0 0 0 0 0 0 5" 29 0 0 2 0 0 0 2 E@
s? April S I - - - - - - -
"E 12(b) _ _ _ _ _ _ _ g 19(b) _ _ _ _ _ _ _ g 26(b) , _ _ _ _ _ _ g May 3 0 3 22 40 0 0 65 10 0 0 0 0 0 0 0 17 (c) _ _ _ _ _ _ _
24 (c) _ _ _. __ , 31 0 0 2 0 0 0 2 June 7 0 0 1 0 0 0 3 14 ICI - - - - - - - 21(0) - - - - - - _ 28 0 2 4 1 0 0 7
u - (Continued) Live Clam Size Distribution Numbers Total' Date 51. 00 (m) 3. 3 5 (nun) - 6. 3 (nia) 9. f isun) ' 17. 50nin) 16. 0 (mm) Live Class July .5 0 0 9 5 0- 0 14 12' O 26 14 12 0 4 56 19 0 28 .19 .4 0 0 51 26 -0 43 69- 1 0 0 113 August '2' 0' 7 6 l' O O 14 9 0 23 44 9 1 0 77 16- 0 8 49 21 0 0 78 23' O 7 45 1 0 .0 53 30 0 8 13 6 1 0 28 0 ! September 6 0 31 23 14 0 0 68 yo 13 20 0 C 30 26 33 40
,15 1 0 79 gg 13 1 0 80 gg I 27 0 8 31 4 2 0 45 P9 October t! E l 5 11 4 0 0
16 4 18 14 9 3 2 1 0 0 45 3C l
- N 22 *9
- 18. 0 2 4 2 0 25 0 7 3 3 2 0
0 8 Of 15 9Q j November 1 0 5 1- 1 0
# 2i l ICI 0 7 r2 ME 8 - - - - - - -
15 0 2 11 17 17 0 47 22 0 0 0 3 2 2 7 4 29' O 4 2 1 3 0 10 December 6 0 0 0 0 ,' 13 0 0 0 0 0 0 0 0 0 0 20 0 0 0 0 0 0 0 27 0 0 0 0 1 0 1 Total 0 290 481 186 35 6 998 I*I Impingement could not be conducted due to high water conditions. (b) Impingement could not be condu:ted due to diving operations in screenhot..e. (c) Impingement could not be conducted due to maintenance. 4 -wi,. ,ei
- p #
~
TABLE V-I-9 2 SIZE DISTRIBUTION OF Corbicula (Clams /1000m ) COLLECTED DURING' IMPINGEMENT SURVEYS FOR ONE 24-HOUR PERIOD PER WEEK,1991 ' BVPS' Live Clam Size Distribution (Number /1000m2 screen) Total 2 Date i 1.00(rs) 3. 35 (m) 6.3(n ) 9.5 (nur) 12. 5 (m) 16.0 (ne) Live Clams /1000m , January 4 (a) _ _ _ ._ _ _ _
.11 0 0 0 0 0 0 0
.18 0 0 0 0 0 0 0 25 0 0 0 0 ~0 0 0 5-February -1 0 0 0 0 0 0 0 g 8 0 0 -0 0 'O O O ,n '
15 0 0 0 0 0 0 0 - c 22 0 0 0 0 0 0 0 EE i
?E=
March 1 0 0 0 0 1.9 0 1.9 !? m >.g 8 0 0 .0 0 0 0 0 3E ' 15 0 -0 0 0 0 0 0 x9 e.- 22 0 0. 0 0- -0 0 0 00 2 29 0 0 3.7 0' O O 3.7 gg 4x April 5 I - - - - - - - 5$~'E 12'DI - - - - - - - g 19(b) _ _ _ _ _ _ 26(b) _ _ _ _ _ _ May 3- 0 4.2 30.8 56 'l 0 0 91.1 10 0 0 0 0 0 0 0 17(c) _ _ _ _ 24 (c) _ _ _ _ _ 31 0 0 2.8 0 0 0 28 4.2 0 0 0 l June 7 . 0 0 t 14 (c) _ _ _ _ Cl(c) _ _ _
.28 0 2.8 5.6 1.4 0 0 9.8 t t
EDIF, V-I-9 (Cmtinued)
- Livif'I4 i n 01stribution
~
2 Date (Number /1000m screen) Totcl
$ 1. 00 (mm) . j ,[?[, 6.3(mm) 9. 5 (mm) 2
- 12. 5(nun) 16.0(mm) Live C' lams /1000m July.. .5 O. -. 12.6 7.0 0 'O 19.6-12 0 48.6 25.2 22.4 -
0 - 7. 5 . 104.7 19 0 52. 3 35.5 7.5 0 0 95.3 26~ 0 60.3 96.7 1.4 0 0 158.4 i August 2 0- 9.8 8.4 1.4 0 0 19.6 9 0 32.2- 61.7 12.6 ' l.4 O 107.9 16- 0 11.2 68.7' 29.4 0 0 23 0 109.3 9.8 63.1 1.4 0 0 74.3 ' 30 0 11.2 18.2 8.4 1.4 0 -39.2 g o Erptember 6 0 43.5 32.2 19.6 'O 5* O 95.3. 13 0 42.1 46.2 21.0 , 20 0 36.5 56.1 18.2 1.4 1.4 0 0 110.7 gg 27 0 11.2. 43.5 5.6 2.8 0 112.2 gg 63.I t- ta z N October 4 0 22.4 25.2 12.6 2.8 0 63.0 E"
< r*
11 0 19.6 A A 18 0
- 5. 6 2.8 4.2 1.4 0 30.e 5E!
g=.
*6 .
2.8 0 0 11.2 -H i 25 0 13.1 5. 6 ' 5.6 3.7 0 2e.0 !h November 1 N3 0 9.3 1.9 1.9 0 0 13.1 $5 8(c) _ _ _ _ _ _ _ ,5 i 15 0 3.7- 20.6 31.8 31.8 0 87.9 22 0 0 0 -5.6 3.7 3.7 h 29'- 0 13.0 g 7.5 3.7 1.8 5.6 0 18.6 December 6 0 0 0 0 0 0 0 13 0' 0 0 0 0 0 i 0 20 0 0 0 0 0 0 ' 0 27 0 0 0 0 2.8 0 2.8 Total 0 440.1 698.4 279.7 62.1 11.2 1,491.5 (a) Impingement could not be conducted due to high water conditions. (b) Impingement could not be conducted due to diving operations in screenhouse. ICI Impingement could not be conducted due to maintenance. i I a
DUQUCStic LIGIIT COMPAtdY 1991 Allt10AL ctNIRONMCt4TAL REPORT WATER TEMPERATURE RIVER ELEVATION VATER TEMPERATURE (oF) RIVER ELEVATION (f t.) 100 --- 674.0 80 --~ - -
;wCb - x' ------ -- - 672.0
\
[> \ 60 A- + ~~---f-
--- &-[ -'- 670.0
/
\
L v' s
/
40 W - -- - - - - " " ~ - - - - -- - - - - - - - " - g.;- 666.0 20 - -- - - - - 666.0 4;;; 9 - % g- - ,;;;;;, - - - - - - - - - --- H 0
'''''''''''''''''''''''''''f'664.0
. . - _ - _ - - . . - . - . . _ ~ _ . . . _
5 50 - __
~'
W y . - - 1 40- ~ 8 8- _ _ _ _ _ _ - . __ _ _ . _ . . _ _ . _ - _ _ . . , !o 30-s g _- E m 20-d /c:r/ o /o/ M o as/ c h 16.0 an d 10 -
/o/o/w/ m / w A 12. 5 an z fo/o/Of Eu / O h 9 s an y /c/w/w/ / a=rA 6.3 ma y / O /s.=7/c=r/ / ,
/ C + 3.35 an
, /c=1/ a / o f / c r f o / c;ri f o i / a:;ri / o i f o f,o_ _f $1,00 ac ; O i i i i, i i i i l JAN FEB MAR /.PR MAY JUN JUL AUG SEP OCT NOV DEC ! 1991 I = Ne Imoingement surveys conducted in April due to diving operations. l FIGURE V-I-7
)
2 ' SIZE DISTRIBUTION OF Corbicula (Number /1000 m Screen) AVERAGED FOR EACH MONTil FROM MEEKLY IMPINGEMENT SURVEYS, 1991 DVPS 145'
I DUQUESNE LIGilT COMPAllY l 1991 ANNUAL ENVIR0tiMl71TAL REPORT - l 1 3
>13000 l l
t
.s s-'
23:0 ! i 800 Y i 800 l h ! 400 - 200 - g i4 A .,, ,, . , u, ,, , _ , E' - g ,
)P sis J J A sou c l J P w Au, J a some l J P ulws ) A eoma l h P u15) J A eouslJ PE AuJ J A sons lj P ulwJ J Agono mA[A l ,
( 81 82 83 84 86 86 . A 13000 4 12,362 Q \
~d
[f 23:0 s y , p 2 2C3 A e00 6 le [
< :0
)
d g , GOD ~ -- t .
- I --
l.300
~
i I i_ ,, . -- -
,i,'. -: ,i h
. .. L b,
a/ % 4 JPW/ 4J J AsoN0 l)PW1MJ J AgoNDl J P M JJAtoN9lJPudWJJASON0ldwAWJJA8cMo 47 46 89 90- 91 I' DEAD -+* ALIVE
~
DATA POR NOVEMBER AND DECEMBER 1989 REPRESENTS ONLY ONE SAMPLING > PERIOD FOR EACH MONTH DUE TO EITHER DIVING OR MAINTENANCE. l' L l~ FIGURE v-I-8 4 L f
SUMMARY
' OF Corbicula _ COLLECTED FROM Tile INTAKE STRUCTURE TRAVELING SCREENS.DURING IMPINGEMENT SURVEYS, 1981 TilROUGil 1991 BVPS h .
l-l 146
.. - . - - - . . . . _ = - .- _ -- -- .- . .- . - .- -.-
DUQUESNE LIGilT COMPANY 1991 ANNUAL ENVIR0 tim"4TAL REPORT Summary Sampling of sediments in the Unit 1 cooling tower lower reservoir was performed on April 18, 1991 during a sche $uled outage, in order to estimate the Corbicula population within that structure. The. Corbicula population in the reservoir was estimated to be 160.0 million clams (99.9% dead), based upon the beventeen ponar dredge samples collected. I The results of the Unit 1 cooling tower population survey confirm the effectiveness of the CT-1 molluscicide dosings in killing Cor bl eul t. present in that structure. All clams were removed frcn the Unit 1 cooling tower basin during this outage. Popula ti^n survels of both BVPS cooling tower reservoirs conducted during scheduled outages (198( through 1991) have resulted in lower eatimates of Corbicula in the Unit 2 tower ccupared to the Unit 1 cool-ing tower.. This can be at tribu ted to differences in cooling towerdesign and the f aster water currents in the Unit 2 cooling tower reservoir, which decrease sediment deposition. The river surveys conducted in 1991 demonstrate that Corbicula inhabit-ing the upper Ohio drainage provide a large number of clams to the , BVPS. Corbicula densities in 1991 at sampling stations above and below BVPS remained either steady or were comparablo to densities found in the past two years. Cleaning of the intake bays in the spring and f all by divers resulted in removing many live clams from the inner bays; this along with the weekly impingement data show that adult clams move into the plant with the water currents.
- 2. Corbicula Larvae Study Objective -l The Corbicula larvae study was designed to collect data on spawning activities in the Ohio River and BVPS Units 1 and 2 cooling tosers.
I 147
DUQUESilE LIGIIT COMPAtiY 1991 AtillUAL EtiVIR0 tit 4EtiTAL REPORT I Methods Specially conctructed clam cages (Figur e V-I-1) were utilized for this study. Each cage was constructed of 1-mm mesh fiberglass screening secured within a 1 ft durable plastic f rame, which contained approxi-mately ten pounds of industrial g) Ass beads ( 3 /8 " diameter ) to provide ballast and a uniform substrate for the clams. The clam cage mesh site permits only very small clams or pediveliger larvae to enter and colon-ize the cage. Larval cages were maintained in the intake structore and cooling towers- . l according to the following procedure. Each month, one empty clam cage was placed in each cooling tower and two cages were placed in the intake structure bays. Each cage was left in place for five months, after which time it was removed and examined for clams. A maximum of five h clam cages were maintained in each cooling tower af ter the initial five-month period. A maximum of ten cages were maintained in the intake structure. Each clam cage removed after the five-month colonization perlod was returned to the laboratory where it was washed to obtain the clams which had colonized inside the cage. Corbicula obtained from each cage were rinsed through a series of stacked U.S. standard sieves ranging in mesh - si ze from 16.0 mm to 0.6 mm. Live and dead cl.ms on each sieve were counted and the numbers were recorded. The largest and smallest clams were measured using vernier calipers to establish a length range for the sample. It should be noted that the size distribution data obtained using the sieves reflects clam width, rather than leng th , al though either measurement in acceptable. Results Month).y totals for Corbicula (live and dead) collected f rom larval cages placed in the intake structure and cooling towers are presented in Table V-I-10. The length ranges for the Corbicula collected f rom each cage are also presented in this table. 148
TABLL V-I-10 RESULTS OF THE Corbicula LARF; STUDY IN THE. INTAKE STRUCTURE AND UNITS 1 AND 2 COOLING TOWERS, 1991 BVPS Total sameer cimas Collected Cham Length e te ten! Date intste Structure Cooling Tower Intete *tructe'e Coeling To-ee Cage Cage tege A Caq,B Unit I ennt 2
- p. m t seeoeal Alave M t stor Alte, g a stor Allee M e stor Altee, g 1 mor Cate A Coq
- 8 Uni t 1 Unit 2
~
Dog 10 Jan 1tte.b} 619 4- 0.6 693 . 24 3.3 - - - - - 1.90-12.So 2.23-12.90 - - y sep 21 Feb 18 a.b3 48 4 7.7 149 . 7' 4.3 - - - - - - 1.we. 30 1.30-4.73 - - t Czt 12 sinr.15 e bt ,3_ 1 So.c - e e e.c ' - - - - - - 2.00-2.30 e - - g so, 23 Apr 15'*I 6 0 0.0 0 0 0.9 0 0 0.8 e 8 0.9 0 e c g hh CC os, is = 17'e> . . ... . . ... - - - . 4 2 .. . . - , g: p, Jan 18 Jan 13t al 0.0 z 0 0 8.8 3 0 - - - 23 e s.e e 3.40-4.11 - 6.es-6.eg M t'3 Feo 18 Jul 12I *I 30 0 0.0 332 0 0.0 ' - - - 43 8 0.0 2.W 5.70 G.co-? : M - 11.10-15.73 C H :D O
.A nar 15 Aug 16'*I 152 3 1.9 293 2 0.7 - - -
24 e Se 3.75-18.95 <1.00-24 $ -
- 3. 30-19. se Q%
w n Apr 15 sep 203 *I S2 2 2.4 997 le ' 1.1 - - - o 3 100.3 C .se-la.55 2.30-25.45 - D h r3
%O mer 17 Oct 7'*I 268 12 4.3 632 13 2.3 - - -
0 4 100.0 Q .00-20.50 1.50- 22. 50 - 1.35-7.15 y% Jon 13 t' > now 35 344 4 1.1 757 it 1.3 163 19 10.6 2c 4 23.6 3.10-21.30 1.30-19.50 2.00-17.30 2.60-3.93 2 Jul 12 Dec 12 341 27 7.3 473 7 1.4 133 62 31.5 s 3 33.3 <1.00-20. 50 (1.8e-18.00 G.00-16.30 3.ce-7.4c , Aug 16 O-Jos 24 71 9 11.3 429 ? 1.2 6 79 92.9 34 4 15.0 1.40-12.33 G .00-16.45 3.29-9.60 <1.co-T.e s :t*
"i Total 1.954 66 4.579 86 301 159 ISO 30 I*I t> s t 1 cooling tower ca9e piecement for clee secolonisation.
IDI Unit 2 cooling tower ce9e plac eent for clan recolonisetaan.
I Unit 1 cooling tower ce9os reeseed April 15 dee te scheduled oste 9e.
v - - - _ _ . _ _ _ _ - - - _ _ _ _ - - _ - . _ . - _ - - _ _ . - _ _ .
DUQUESNE LIGHT ConPANY 1991 ANNUAL ENVIRONMENTAL REPORT The larval cage which collected the most Corbicula (907 - total of 897 live and 10 dead) was located in the intake structure (sample period April 15 to September 20, 1991). The largest Corbicula found in the larval cages in 1991 was 25.4 5 mm in length (intake Etructure, April 15 to September 20) . Table V-I-11 and Figures V-I-9, V-I-10 and V-I-11 present size distribution data for live clams collected in the larval cages. The intake structure graph illustrates size distribution data which represents the average for the two larval cages which were removed each month. Intake structure larval cages removed on January 18 and February 18, 1991 contained high numbers of juvenile Corbicula (average live 657 and 99, respectively). These clams most likely entered the cages during the l late summer /early f all spawning period and experienced slight to moder-ate growth prior to the decrease in ambient rivkr water temperatures (Table V-I-11). Colonization of intake structure larval cages by juvenile Corbicula from the 1991 spawn was initially observed in cages removed on July 12 (Table V-I-10) . Live Corbicula densities remained high in the cages removed during the remaining months of 1991. Corbicula removed from Antake structure larval cages in August through November were predomi-nantly (62.3%) of the 6.3 and 9.5 mm sieve si ze categories (Table V-I-11). Addi tionally, larger Corbicula retained on the 12. 5 mm sieve accounted for 15.7% of the live clams removed fran the larval cages in the months of September through November 1991. Elevated river water temperatures in the summer and f all (Figure V-I-9) probably contributed to the rapid growth of these Corbicula in the intake stretture larval cages. In 1991, DLC continued its Corbicula Control Program (second year) which included the use of a molluscicide (CT-1) to help prevent the prolifera-tion of Cor bi cula althin the BVPS plant and cooling towers. DLC was granted permission Ly the Pennsylvania Depar tment of Environmental Resources to use this molluscicide in the DVPS Unita 1 and 2 river water systems. The five larval cages housed in the Unit 1 cooling tower were 150
/ ..
TABLE V-I-11 RESULTS OF THE Corbicula LARVAE STUDY SIZE DISTRIBUTIM IN THE INTAKE STRUCTURE AND UNITS 1 AND 2 COOLING E MERS, 1991 BVPS Cage Live Clam Size Distribution Numbers Total Date Location' 51.00 (nun) 3.3 5 (nun) 6. 3 (ast) - '9.5(mm) 12.5(mm) 16. 0 (mm_)_ . Live Clams / Cage
' January 18 Int I8I -
560 75 22 0 0 0 6 57 1 ctIDI - - - 2 ct(b) _. _ _ _ _ _ _ 3 February 18 Int 99 0 0 0 0 0 99 I ctIDI - - - - -- - - E8 2 ct(b). . _ _ _ _ _ _ _ go
? G-March 15 Int 1 0 0 0 0 0 1 n$
1 ct(b).. _ _ _ _ _ _ _ j w 2 ct(D) - - - - - - - ;;E w . g=
~n ~
April 15 Int 0 0 0 0 0 0 0 @o 1 ct ICI O O O O O O O *@3 2 ct - 0 0 0 0 0 0 0 E3z May 17 Int 0 0 0 0 0 0 0 ,$ *
'I ct(c) _ _ _ _ _ _ _
o 2 ct' O O O O O O O June 13 Int 1 1 0 0 0 0 2 , 1 ct IDI - - '~ - - - - 2 ct 0 23 0 0 0 0 23 July 12 Int 103 59 3 1 0 0 166 1 ct(b) _ _ _ _ _ _ _ 2 ct- 0 0 6 37 0 0 43 1 4 _.____-.______-_---..n _
y-_ . _ . _- TABLE V-I-ll (Continued) Cage Live Clam Size' Distribution Numbers Total Date Location 51.00(mm)- 3.35(mm)~ 6.3(mm) 9.5(mm) ' 12. 5 (mm) ,16.0 (mm) Live Clams / Cage August 16 . Int 32 29 121 39 3 0 224 1 ct(b). . _ _ _ _ _ _ 2 et 2 0 0- 14 8 0 24 September 20 Int 38 ~ 79 135 186 52 1 491 1 ct IDI - - - - - -
~
2 et ~0 0 0 0 0 0 0 e 1 October 7 Int 40 62 96 187 65 l et - - - 1 451 gg zo 2 et 0 0 0 0 0 0 0 EN "E November 15 Int 50 77 152 155 118 O 552 E" e- 1 et 59 59 28 12 2 0 160 $C
$ 2 ct 20 0 0 0 0 0 20 QS 3
December 12 Int 69 101 153 53 7 0 383 Eo 1 ct 33 53 41 8 0 . 0 135 E4 4 2 ct 2 4 0 0 0 0 6 w en
.E Total 1,109 622 757 692 255 2 3,437 o 4
(a) Number of clams represent the average of two cages in the intake structure. (b) Cage placement for clam recolonization. . (c) Cooling tower cages removed due to r.cheduled outage. Symbols Int - Intake structure - 1 et - Unit 1 cooling tower 2 et - Unit 2 cooling tower
DUQUES11C LICitT COMPAllY 1991 ANNUAL ENVIROllMENTAL REPORT WATER TEMPERATURE ( a F) i 100 mW k ' 80 n #+R,%p ' - - ~ ~ " -
~
So - 40 %A p^s r - - -
- - - - - - - -- - ~w 2o = _ . . . . . . . - . _ . . . . . . - - . . . . . . . . . . . . . - . . -
l l 1 1 1 1 ! I I t iii! I f ! t 1 1 1 1 1 1 1 1 1 1 1 i i i1 ! i i ii1 8 i'1 I f f f 1 I i 1/11 2/16 3/15 4/12 5/10 6/14 7/12 8/16 9/13 10/11 11/ 8 12/13 DATE UNIT 1 COOLING TOWER -+- UNIT 2 COOLING TOWER kNI2 EN$N, fyj' -+- INTAKE STRUCTURE 560 NUMBER OF CLAMS PER SIEVE SIZE
/
INTAKE STRUCTURE
. - - - . . - - . ~ . . -- . . . - - . . - -
250 - 200 - _ _ - _ _ . . . . . . . . . . . . _ _ - . . . ._~.- .-- - 150 - I'00 - l
;7/c/a/c/.-- 16. 0 na 60 - '/ =/ O / " / = M 12 ' "
/ c / c / O / O /.M 9. 5 m.a c / c / c / O f CM 6.3 an i 7/0/O/O/CM 3. 3b an \
0'i
^
r 'f'f'f'f'I i i
~
i i i 1/18 2/18 3/16 +/15 6/17 6/1? 7/12 8/16 9/2010/711/1512/12 CAGE REMOVAL DATE FIGURE V-I-9 RESULTS OF Tile Corbicula LARVAE STUDY SIZE DISTRIBUTION IN Tile INTAKE STRUCTURE, 1991 BVPS l l 153 i I - . . - .--.. - - - . .~
DUQUESNC LICitT COMPANY 1991 AN!10AL ENVIRONMENTAL REPORT WATER TEMPERATURE ( a F) 100 Y *l% . s. 60 - - - - - - -- -- h-(-- - 60 g*-? ----- -
- 3. -- g H' %.
g ..-.._..-__,-_..........sS. v*g 4gj Ag_ .- _ _ 20 - - - - - - - - - - - - - - - - - - - - - - - - - - 0 1/11 2/15 3/15 4/12 6/10 6/14 T/12 8/16 9/13 10/11 11/ 8 12/13 DATF
-- UNIT 1 COOLIN f. TOWER -*- UNIT 2 COOLING TOWER (Unit I scheduled outage -+- INTAKE STRUCTURE Apr.12 to July 20. 1991)
NUMBER OF CLAMS PER SIEVE SITE UNIT 1 COOLING TOWER 250 -
- _ __ - . . - ~ . . .
200- - 160-100 -
/~ / / / O Awd / / / aan / O A 1s.o m
/ / / /O k a"f / / / km ' n ' 12. 5 ma 50- / / / / O p. -y / / / m EL 9. 5 aa
/ / / /OP / / / / / M 6.) ma
/ / / / O AMnf / / / / M 3. 3 5 mm
/
/. /, fo, # rdV / / / / / < 1. 0 0 ma 0 . i i i i i i i i RECOLONIZ ATION 4/16 OUTAGE RECOLONIZATION PERIOD 11/16 12/12 PERIOD ** CAGE REMOVAL DATE n Recolonization period af ter 1990 Cathicula Control Program f all mollueelcide dosing FIGURE V-I-10 RESULTS OF Tile Corbicula LARVAE STUDY SIZE DISTRIBUTION IN Tile UNIT 1 COOLING TOWER, 1991 DVPS lb4
- - _ _ - _ = _ - _ _ - __ - - _ _ - _ _ _ - _ - _ _ _ _ - - - - - _ - - _ _ _ .
DUQUESNE LIGHT COMPANY 1991 AliNUAL ENVIRONMENTAL REPORT WATER TEMPERATURE ( o F) 100
^M WN 80 ------
% **W' '& - W~ - - ------ -
h -- -- lj'% 4 w 60 - -- - ~ ~ -- > -----------
-y--g H \-
4vr 3 / ' ~g% b4 9v 20 - - - - 0 1/11 2/15 3/t3 4/12 5/10 0/14 7/12 8/16 9/13 10/11 11/ 8 12/13 DATE
- UNIT 1 COOLING TOWER -+- UNIT 2 COOLING TOWER (Unit 1 scheduled outage -+- INTAKE STRUCTURE Apc.12 to July 20, 1991)
NUMBER OF CLAMS PER SIEVE SIZE UNIT 2 COOLING TOWER 250 - 200 - 150-100 -
. / _/ / /C;r/ O / ' .=2 /O /4=r / t=7 / 4=7 / c=r / 16. 0 5
. / / / / O / 4=? /4=? M ;7 / 4=7 / c 7 / a=r / 4=*; g 2,5 a 60 - / / / / c=r / c;1-< 0 /p / O / O / c r / c=r ; , , s ,,
/ / / / t=7 / c"7 M > / N/4=7 / t=7 / O_/ c"7 / C 9 / g , ,s ,,
f / / / t=7 / O / M'/ C='/ 4=* / 4=7 / 4=7 M V7 / W_/ 3, 3 $ ,, O
/
i
/
i
/
i
/ 4=7 i
/ 4; 7 /i 4=7i / 4=7i / Q i / t=7i /4=7i / M/ QJ g$ , ng ,,
i i RECOLOHlZATION 4/15 5/17 8/13 7/12 8/10 9/20 10/7 11/15 12/12 PERIOD CAGE REMOVAL DATE FIGURE V-I-ll RESULTS OF TIIE Corbicula LARVAE STUDY SIZE DISTRIBUTION IN Tile UNIT 2 COOLING TOWER, 1991 BVPS 155
DUQUESi1E LIGHT COMPAt1Y 1991 A11NUAL EFIVIROt1 MENTAL REPORT lef t in place during the molluscicide dosing on December 10, 1991. The Unit 1 cooling tower larval cage removed on December 12 exhibited only 31.54 mortality (62 dead Corbleula) . Mortality was higher (92.9%) in the larval cage removed f rom this structure on January 24, 1992. These mortalities are lower than those obtained during the previous Unit 1 CT-1 dosing of June 1990, where 100% mortality occurred in the larval cage removed approximately three weeks af ter dosing. Colonination of Unit 2 cooling tower larval cages was initially observed on June 11, 1991 (Table V-I-10, 23 live Cor bicola) . The number of juvenile Corbicula entering these cages remained rather low for the months of July and August, ccmpared to the large influx of clams enter-ing intake structure cages. The Unit 2 river water system was treated with the molluscicide CT-1 on August 21, 1991 as part of the Corbicula Control Program. The five larval cages housed in the Unit 2 cooling tower were left in place during the molluscicide dosing. The larval cage removed one month after dosing (September 20) had 1006 mortality (3 dead Corbicula) . Recolon-ization of Unit 2 cooling tower larval cages exposed to the molluscicide was first noted in the cage removed on November 15 (20 31ve Cor bicula) . The larval cages removed in December and January also contained low numbers of Cor bicula, similar to the totals from the pre-dosing months (J une-Aug ust ) . Summary Cor b' :ul a , which colonized the larval cages housed in the BVPS intake nructure during the summer of 1991, exhibited vigorous growth during the five-month colonization period. Almost half (47.0%) of the live Corbicula removed from the i n'ta ke structure la val cages in August thr ough November were retained on the three largest mesh size sieves (9. 5, 12.5 and 16.0 mm) during the size analysis. Elevated river water temperatures throughout tht summer and early fall probably contributed to the rapid growth of these clams, in conjunt: tion with an adequate food source for these filter feeders. 156
, DUQUESHE LIGiiT COMPANY 1991 ANNUA!. ENVI RONCc!TAL '.CPORT The use of CT-1 molluscicide (1991 DLC Cor bicula Control Program) on ql December 10, 1991 in tnv Unit I river water system produced 31. 51 mor-
~*
tality (62 dead Cot bicula) in the la'. va l cage removed from the Unit 1 h cooling tower on December 12 (two days post-dosing). Mortality was b greater (92.9%) in the la; val cage removed f rom this BVPS structure on January 24, 1992.
. e Unit 2 cooling tower 1.arval cages contained le numbers of Cor bicula b
Uzot greater than 45 per month) during the 1991 monthly sur veys. The l,. %
, ' "f ese of CT-1 molluscicide in the Unit 2 river water system on August 21, 1991 produced 10M mortality (three dead Corbicula) in the larval cage emoved one month af ter dosing (September 20). Recolonization of Unit J 3 larval cages exposed to ' the molluscicide was rirst noted in the cage a removed on November 15 (20 live Corbicula). The recolonization of molluscicida 3xposed larval ceges was previously noted 6uring the CT-1 molluscicide dosing of the Unit 1 cooling tower on June 20 and 21, 1990. Both studies tend to indicate that no residual sediment toxicity i-evident after CT-1 molluscicide application.
- 3. Pc4 td . i t., r.rcwth S tudy Objectiva '
t The growth study examines the maximum growth attained by Corbicula which colonize the larval cages placed in the BVPS intake structure and cool-
.ng towers.
Methods Empty larval cages were placed in the intake structure and Units 1 and 2 cooling towera each month to determine the maximum growth of invading larvae over a five-month period of colcrization. The length and width of the largest Corbicult. found in each larval cage removed after the tive-month colonization period had been measured to the nearest 0.05 mm usho Vernier calipers. The larvae study began in August 198C (initial cage placement) and has continued through D ece m'>e r 1991 (cage removal 15 '/ l 1
I DUQUESNE LIGHT COMPANY.
, 1991 ANNUAL ENVIRONMENTAL REPORT ^
after July _ 1991 placement), resulting in a five-month colonization period per evaluation. Results Table V-I-12 lists length data for the largest Corbicula found in each iarval cage removed from the BVPS intake structure and cooling towers
-over the past four years. The largest Corbicula ever collected from a larval cacje attained a length of 25.50 mm ~ (intake. structure, sample perio$ May to October 1988).
The largest Corbicula collected to date from a Unit 1 cooling tower larval. cage measured 17. 90 - mm in length (Table V-I-12) . The maximum length obtained to - date for - a Corbicula from a Unit 2 cooling tower larval cage was 19. 50 mm (sample peric.' March to August 1991), which represents a 3.75 mm increase from the previous maximum length of 15.75 mm (May to October 1988) .
.- * . j Summary i
Corbicula larvae which colonized the intake structure larval cages !
- during the summer and early fall have shown rapid growth and reached ;
larger sizes than -those ' entering the cages -during the winter and early
- spring. Corbicug _ removed f rom the Units 1 and 2 larval cages generally t ve not attained the maximum-sizes observed for clams removed f rom the
's intake structure cages for the same period. This may be dua to chlor-ination in the' cooling towers.
J. ZEBFA MUSSEL MONITORING PROGRAM
-Introduction
. Zebra mussels .(Dreissena polymorpha) are exotic freshwater mollusks that look similar _ to marine barnacles, and have brown shells marked with
._ alternating zig-zag yellowish bands. They are believed to have been introduced into North America through the ballast water of ocean-going 158
'm.8
. , t m .
_ . - ^.a x. - y - n m?- \,: f, y V +
,_ ) ,
l
' ~ '
.3 O . '- , ..# , ,_
vy 3 ,
~ ~
d g j 4 .! h E- _ r. . L TABLE V-I - MAXIMUM (.orbicula GROWTH ' LENGTH ACHIEVED IN A' FIVE-MONTH . PERIOD
' SL49ERIZED FROM THE. IARVAE~ STUDY CAGE COLLECTIONS
~
1988 THROUGH 1991J -
< :BVP?
"Date' Maxistan Clan Growth I.ength (mm)
. Cage . Cage, Intake Structure H Unit 1 Cooling Tower- ' thsit 2 Cooling Tever
-PlacementL IRemoval 1988 '1989 1990 : '1991 "98, 1989 19 M 1991- 1988 -1989 1990 1991" '
18.10 :- 13. 10 : 12.90 August.- ; January - -
-7.95 ~' - -
3.65' L12.7, 0 . -- _yg
-ZC.
September. February .- 9.85 '4. 50 ' 4.75 -' 9.70 - - - 0 8.40' - z so -
. C C-
> (9 October March - 4.00. ' 1.00 2.50- -
9.30' - ' - :- : 5.10 6.20 - t- m
-z~
+ nn. Itovember ' April - 8.40 'O 0 - 4.35 - 0 - - - 4.70 '0. (g mm
'W ut December 'May -
7.30 'O O -- 3.10 - - - - 7.00 01 29: Q-.e
.e January June' 6.70- 0. 5.70- '6.15 .0 5.10 6.55 - 0 -
- 11. 50 8.80 % o -.
1 -
- February . July 16.00 '7.8*- 13.25 '15.70 9.55 9.30 9.20 - 9.25 -
10.65 15.7$ $ .o . ' ta >' March . August' 21515 17.20 17.20 20.65 16.00 13.40 10.75 - 12.75 - 12.25 19.50 [ s .. ,
. April september 23.90 19.20 17.10 25.45- 15.00 '13.20 .14.70 - 13.10 - - 0 o t
- c .
May October 25.50 20.10 19.30-. 22.50 . 17.30 - 16.30 - 15. ~ 11.60 - 7.15
' Jc te November 21t.r3 .14.90 18.30, 21.30 17.90 -
15.20 17. 50 D.45 11.70 - 3.90 . July -December 21.00 15.45 16.90 20.50, 16.50 - - 16.30 9.70 13.10 - 7.40
=b
(-t No data was collected due to plant operations. k
.___.-.___z_--_.= _ _ - _ - _ _ - - . _ , . . _ . s.~:.- r a > n s , m . . , _ _ _ - ,
_ s c.__, ~_-. _.m _ _ue .___2 . _ . . _ _ - . _ _ _ _ . -
DUQUESNE, LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT They first appeared in Lake cargo vessels probably from Eastern Europe. St. Clair in 1987 and have spread rapidly to other Great Lakes and are expected to inf estate the Ohio River in the near future. Adult zebra mussels can live up to five years and grow to two inches in length. Each female is capable of producir.g 30,000 microscopic (veliger larvae) offspring per year that can easily pass through water intake screens. They use very adhesive hairlike (by ssus ) threads to attach themselves to any hard surfaces (e.g . , boat haulc, intake pipes and bodies other mussels). Transpor tation of these organisms between water is acceroplished in part by boats havinq adult massels attach ta their BVPS, in anticipa-hauls or larvae in their live wells and/or bilges. tion of this possible inf estation and responding to NRC Notice No. 89-76 (Blofouling Agent-Zebra Mussel, 21 November 1989), instituted a Zebra Mussel Monitoring Program in January 1991. The Zebra Mussel Monitoring Program includes the Ohio River and the c! r-culating river water system of the BVPS (intake structure and cooling resulta towers). This report describes this Monitoring Program and the obtained during field and plant surveys conducted through 1991.
- 1. Monitoring Ob%c tives The objectives of the Monitoring Program were to BVPS
- Identify if zebra nussels are in the Ohio River adjacent and provide an early warning to operations personnel as to their possible infestation.
- Provide lif e history data as to when the larvae are mobile in the Ohio River and provide insights as to - their vulnerability to potential treatments.
160
i 1 ' DUQUESNE LIGHT COMPANY 1991 ANNUAL ENVIRONMENTAL REPORT
- Provide data as to their growth rates ur. der different water tem- 1 1
~
peratures and provide estimates as to the time it requires for l these mussels to reach clogging size. Methods I
-(Intake Structure) !
l
- Artificial substrates des 3gned to :;onitor for zebra mussel colonization
-frcn the Ohio River were placed in the intake structure at BVPS (Figure V-I-1) .
The mater al used in the construction of these artificial substrates was plas tic utility _ cartons (milk cartons) which were cut l
, - along ' the seams ~on _ the sides and ' bottom. Each carton
- yielded five !
pieces of plas tic with varying _ size openings and edges , that contain tight angles which add to the overall surface area. Each unit consisted
' of - two cut cartons. These ten pieces were , stacked and secured with stainless steel eyebolts. The completed unit had an ove t_ dimension of '~ approximately one square foot. With ten pieces of plas tic, each j
having two sides and apprealmately 50 % open space, this provided an s overall surface area of approximately ten square feet per unit. In order to maximize the efficiency for deployment and retrieval of these substrates, 'one artificial substrate was placed on each of the corbicula larval clam cage anchoring ' lines located- in the - intake struc-ture between the traveling screens - ald . trash- rakes (Figure V-I-M . The zetra mussel substrates were rotated on the same monthly schedule as the corbicula - larval cages- (Section I-2, Methods). After the five-month period -in the water . column, the substrates were removed, -washed, and examined for- zebra musuls identical to the Corbicula Monitoring Program. Since - twu units were placed in service per month for five months, this resulted in approximately 100 square feet of surface area constantly -being available for colonization if these organisms were in t the water column. In - addition to the artificia) substrates specifically designated for zebra mussel su6 veillance, the Corbicula larval clam cages were also 161 4: e e- w e --
DUQUESNE LIGitT COMrANY 121 ANNUAL. ENVIRONMENTAL REPORT v inspected for .' zebra mossel colonization (Figur e V-I-1)'. Experience with collecting these mussels on the outside of identical cages used in Lake Erle during ;the summer of '1088 has demonstrated the suitability of these substrates as good monitoring devices. Two other surveillance techniques used 'in the intake structure were:
- 1) the weekly ~ impingement monitoring program, and 2) obser vations of the divers daring regularly scheduled cleanout operations.
' (Cooling Towers)
The cooling towers - were monitored for zebra mussels using three tech-niques: 1) checking the outsides and contents of the Corbich larval clam cages that were already in place, 2) checking for zebra mussels as part of the cor bicula. popula tion survey conducted .oring regularly acheduled . outages ' (Unit 1 in.1991) , e.nd . 3 ) chec? ting - the walls of tuth reservoirs' and the louvers for Unit 1. (Ohio' River Shoreline) ' Each week,- in ccajunction with the regule- Impingement survey, the BVPS discharge . area was observed for fish, . waterf owl and beaver ac tiv i ti es . In 1991, ' th'e discharge area, along with ~ the barge slip next to the Unit 1 cooling tower, were ~ de signated as observation zones for zebra mussels. The pilings and rocks were checked for coloni zation since
-these organisms will attach to any hard surface.
j (Commun,. ations Network) In 1991 there was , an informal communication network es tablished for zebra mussel movements within trie Ohio River. This included an exchange of information between government agencies, univer si ti es , industrial water users, and other electric utilities. The Pennsylvania Department of Environmental Resources is developing a formal program for 1932 and / BVPS is dedicated to cooperation in this communications program. l 162
~- - . .. .
DUQUESNE LIGHT COMPAtfY 1991 AllNUAL ENVIROtiMENTAL REPORT hesults The results of the 1991 Zebra Mussel Monitoring Program have tevealed that no zebra mussels were collected in the plant or in the Ohio River adjacent to BVPS as part of any sampling activity. In 1991, there were two separate, _ confirmed -reports of zebra mussel findin9s, one in the lower- Ohio River and the other in the Susquehanna River (Pennsylvania). In view of the rapid expansion of these organisms within the Great Lakes . and these most recent sightings, BVPS is vigilant to their potential arrival in the upper Ohio River. Summary The _ zabra - muss'el (Dreissena polymorpha) is an exotic f reshwater molluck f= chat ir Imlieved'to have -been introduced into Lake St. Clair in 1987 via ballast water'of ocean-going cargo vessels. Since then they ht ee spread rapidly to the Great Lakes and are inf esting f reshwc';er systems in the United States. Due to the proximity of the Ohio River to Lake' Erie, BVP3 initiated a Zebra Mussel Monitoring Program in January 1990. The Zebra Mussel-Monitoring Program utilizee artificial substrates which provide a large surface area for the mussel larvae to attach.- In 1991, as the result of plant:and river sampling, no eebra mussels have been detected. 163 m
DUgUESNE LIGIIT COMPAthy 1991 ANNUAL -ENVIRONMENTAL REPORT VI. REFERENCES _Berch, J. Q.,~1944. Checklist of West American Mollusks. Minutes, Conchology Club of Southern Cullfornia 38:18. Commonwealth of Pennsylvania, 1985. Pennsylvania's Endangered Fishes, Reptiles and Amphibians. Published by the Pennsylvania Fish Commis-sion. Counts, C. C. III, 1985. Distribution of Corbicula fluminea at Nuclear Facilities. Division of Engineering, U. S. Nuclear Regula wry Com-mission. NUREGLCR. 4233. 79 pp. Dahlberg, M. D. and E. P. Odum, 1970. Annual cycles of species occur-rence, abundance and diversity in Ge 791a estuarine fish popula-tions. Am. Midl. Net. 83:382-392. DLC, 1976. Annual Environmental Report, Non-radiological Volume fl. Duquesne Light Company, Beaver Valley Power Station. 132 pp. DLC, 1977. Annual Environmental Report, Non-radiological Volume fl. Duquesne .Iight Company, Beaver Valley Power Station. 123 pp. 'l l OLC, 1979 Annual Environmentel Report, Non-radiological Volume fl. l Duquesne Light Company, Beaver Valley Power Station. 149 pp. DLC, 1980. Annual Environmental Report, Non-radiological. Duquesne Light Company, Beaver Valley Powet Station, Unit No.1.160 pp. DLC, 1981. Annual Environmental Report, Non-rad.ological. Duquesne Light Company, Beaver Valley Power Station, Unit No. 3. 105 pp. + Appendices. DLC, 1982. Annual Environmental Report, Non-rad'ological.
. Duquesne Light Company, Beaver Valley Power Station, Unit No. 1. 126 pp.
DLC, IS83. Annual Environmental Report, Non-radiological. Duquesne Light -Company, Beaver - Valley Power Sta tion, Unit No. 1. 124 pp. + Appendix. l_ DLC, 1984. Amual Environmental Report, Non-radiological. Duquesne L19 at Company, Beavi.tr Va. ley Power Station, Unit No.1.
. 139 pp.
DLC, -1985. Annual Environmental Report, .Non-radiological. Duquesne ' Light Company, Beavor- Valley Power Sta tion,' Unit No. = 1 & 2. 106 pp. DLC, 1986. Annual Environmental Report, Non-radiological. Duquesne Light Company, Beaver Valley Power. Station, Unit Nc.1 & 2. 152 pp. DLC, 1967. Annual Environmental Report, Non-radiological. Duquesne l Light Company, Beaver Valley Power Station, Unit No. 1& 2. 14 5 pp. 164
DUQUESNE LIGHT COMPANY 1991 ANNUAL D4VIRONMENTAL ret' ORT 4 DI.C , 1988. Annual, Environmental heport, Non-radiological. Duquesne Light Company, Beaver Valley Power Station, Unit No. 1 I, 2, 161 pp. DLC, 1989. Annual . Environmental Report, Non-radiological. Duquesne Light Company, Deaver Valley Power Station, Unit No. I t. 2. 145 pp. DLC, 1990. Annual Environmental Report, Non-radiological. Duquesne Light Company, Beaver Valley Power Station, Unit No.1 E 2. 181 pp. Gilbert, C. R., 1964. 1:13 A List of Common and Scientific Names of Fishes from the United States and Canada, 3rd Ed. 1970. American Fisheries Publ. No. 6. Washington, D.C. Hutchinson, G.'E., 1967. A L:.eatise on limnology. Vol. 2, Introduction to ' lake biology and the limnoplankton. John Wiley and Sons, Inc., New York. 1115 pp. Hynes, H. A H., 1970. .The ecology of running waters. Univ. Toronto Prest: Toronto. Jenkins, Harold and Frank Logar, (DLC 'perations O Personnel, BVPS) personal communication, December 3, 1985. N RC , IE. Bulletin 81-03: Flow Blockage of Cooling Water to Safety System Components by Corbicula sp. (Asiatic Clam) and Mytilus sp. (Mussel).
- Pielou, E. C., 1969. An introduction to mathematical ecology. Wiley Interscience, Wiley t. Sons, New York, NY.
Robins,-C. R., R. M. Bailey, C. E. Bond, J. R. J rooke r , E. A. Lachner, R. H. Lea, and W. B. Scott, 1980. A List of Common and Scientific Names of Fishes from the United States and Canada (Foutth edition). Amer. Fish. Sco. Spec.. Publ. No. 12:1-174. Shiffer,- C., 1990._ Identification Guide to Pennsylvania Fishes. Pennsylvania Fish Commission, Bureau of Education and Information. 51 pp.
' Winner, J . ii. , 1975. Zooplankton. In: B. A. Whitton, ed. River ecciogy. Univ. Calif. Press, Berkeley and Los Angeles. pp. 155-169.
9 165
- 1. ,
l i l
.l n.
A v-APPENDIX
- 1991 CORBICUIA CONTROL . PROGRAM ENVIRONMENTAL FATE AND EFFECTS ' STUDIES -
I SUMMER AND FALL DOSING STUDIES , Duquesne Light Company Beaver Valley Power Station s x s
-*The appendices oC this report which contain raw data and other
. supporting information are not-included in this' summary, however, this1 data is available by contacting the Director of Environmental
.. Services, Duquesne Light Company, Leave Valley Power Station, Shippingport, PA. 15077 (412-393-5873).
_ =.g g
1991'CORBICULA CONTROL PHOCRAM ENVIRONMENTAL FATE AND EFFECTS STUDIES - SUK*ER AND FALL DOSING STUDIES Duquesne Light' Company Beaver Yalley Power Station D 4 4
-f .\',
.a
{
, QW s -R i s,8 j f ?#:
et 1991_CORBICULA CONTROL PROGRAM ENVIRONMENTAL FATE AND EFFECTS STUDIES - _ SUMMER AND FALL DOSING STUDIES
-_Duquest.e - Light Company
-Beaver _ Valley. Power Station u
{ by-
' Donald S. Cherry. Ph.D.,
. Joseph R. Bidwell, Annick Mikailoff.
1 Mindy M. Yeager and Stuart R. Lynde
- Departmest of Biology,and University Center for Environmental'and Hazardous: Materials Studies,
,+ ' Virginia Polytec' nic ' Institute and State University..
(Virginia Tech) Blseksburg, VA 24861 , A
- . Robert L. Shema-
, Vallian-R. Cody-
.Cary J. Yenderee
-Michael'F. Davison Michael R. Noel-
, Gregory M.HStyborski Aquatic Systems 1 Corporation
-Pittsburgh,- ?A 15282 -
t J. Wayne McJntire C Duquesne-Light' Company-
'Shippingport, PA 15877
, +
f, : February 14, 1 J _.)
?
- . l
- 1 a l r
V- , , t -
- . - . ~ - _ . .
k . 3I
, :C F
STABLE OF CONTENTS page s
"EIECUTIVE
SUMMARY
.'............................ ........................... v 1 *. 0 INTRODUCTION..............a.. ........................................ I 1.1 Overview........... 4.. .......................................... 1 1.2 Toxicity Testing and Face / Effects Strategy. . . . . . . . . . . . . . . . . . . . . . . 1 1 3 P l an t L o c a t i o n . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 1 . 4 R e c e i vi ng Wa t e r B o dy . . . . . . . . . . . . . . . . . . . . . .. . . . . . . . . . . . . . . . . . . . . . . 2 1.5 Testing Laboratories............................................. 2 '
- 3. 0 ' P L ANT OP ERAT I O NS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 2.1 Products........................................................ 2
- 2. 2 Vo l ume o f Vas t e Fl ow . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2
; 3 '. 0 - j SOURCE OF - EFFLUENT AhD DILUTION WATER . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 ,
, 3 .1 Ef fl u e n t - S amp l e s . . . . . . . . . . . ~. . . . . . '. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . : 2 g.. 4.8 TEST METHODS AT VIRGINIA TECH.....
- ................................ 3
-' e' 4.1 Ceriodaphnia dubia and Fathead-Minnow 3'
; 48-br- Acut e - Toaic ity Tes t s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3 4.1.1= Test Methods:Used......................................... 3 ~
14.1'.2 Endpoints of Test.......................................... 3 l4.1.3' Details'of i'est............................................ 3
- 4.2 CeriodaphniaJ dubia S tryival ' and Repr oduction. . . . . . . . . . . . . . . . . . . . 3
~4.2.InTest. Methods Used.............. ......................... 3 14.2.2' Endpoints of Test.......................................... 3 4 2.3 Further ' Description of Testing Protocol . . . . . . . . . . . . . . . . . . . 3 4.2.4 Date and Time Tests Began.........................~........ 4
- 4. 2. 5 Dat e and . Time Te s ts Ende d. . . . . . . . . . . . . . . . . . . . - . . . . . . . . . . . 4 l4.2.6-Type.offTesc Chambers..................................... 4
-4.2.7 Volume of, Test Solution per-Chamber....................... 4
- , . 5' . 8 Number of Organisms s er Chamb e r . . . . . . . . . . . . . . . . . . . . . . . . . . 14 -
4 .2. 95 Number-of Replicate-Test Chambers per Treatment............ 4
;4.2.19 Acclimation of Test Organisms............................ 5 4.2.11 Tect Temperature............ ............................ 5 4.3 Fathead.Miinew-Burvival and $rowth ............................. 5 .
4.3.1 Test-Method:Used.......................................... 5 4 '.3 2 2 Endp o int s of Te s t . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5
- 4.3.3 Further Description of Testing Protocol................... 5 s 4. 3. 4 Dat e - and Time Tes t s Beg an. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
6 ,
.4a3.5 Date and Time Tests Ended..........;...................... 6 ?
4.7.6 Type of, Test Chambers..................................... 6- ' ' 4.3.7: Volume of Test Solution-per Chamber....................... 5-4.3.8 Number of Test Organisms per Chamber....................... 6 14.3 9" dumber of. Replicate Test Chambers per Treatment............ 6 14 . 3 .1 8 T e s t . T e mp e r at ur e . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 4.4 Ceriodachnia dubia Culturing.................................... 6
-4.4.1 Age.......................................................6 1
I
& _ -,g -,s
i
'4.4.2-Life Stage................................................. 6 e
, 4 . 4 . 3 - M e an L e ng t h an d V e 1 gh t . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 4 . 4 . 4 S o ur c e . . . . . . . . . . . . . . . . . . ................................. 6
_ '4.4.5 Diseases and Treatment..................................... 7 i 4 . 5 Fat h e a d Mi nn ow ; Cul t ur i ng . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .... 7 4.5.1 Age................,...................................... 7 4.5.2 Life Stage................................................ 7 4.5.3 Mean< Weight............................................... 7 4 . 5 . 4 S o ur c e . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7
-4.5.5 Diseases and Treatment.................................... 7 4.6 Chironomus ripar(' gs Ten-Day Sediment Survival and Crowth . . . . . . . 7 4.6.1. Laboratory Cul',uring............................... ...... 7 4.6.2 Sediment Col 10ction....................................... 7 4.6.3 Test Protoco1............................................. 7 4 . 6 . 4 T e s t i ng Dat e s . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
9 4.6.5 Statistics............................... ................. 10 J
. 5.eL QUALITY AS8URANCE.................................................... le
- 1. . . .
l , 5.1 Ceriodachnia-dubia.............................................. 10 !. 5.1.1 S t an der d T ox i c an t . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10 5.1.2 Dilution Water Used..'...................................... te l 5.1.3'Date and Time of Reference Test............................ 10 l , 5.1.4 Reference-Toxicant-Results................................ 18
- 5.1. 5, Physical _ and' Chemical Methods Used. . . . . . . . . . . . . . . . . . . . . . . . . 11
= 5 . 2 . rat he ad' M i nnow . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11
'5.2'T Standard Toxicant.......................................... 11 5.2.k1Date:and1 Time of Test...................................... 11 5.2.3 Dilution Water Used........................................ 11 5.2. 4 Referenc e Toxicant Resulta . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11
- 5 2. 5 Physical mui Chemical Methods Used. . . . . . . . . . . . . . . . . . . . . . . . 11 7 6.8 ON-CITE EXPERIMENTAL STREAMS LA BORATORY. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12 6.1 Erperimental.Streant Design.~..................................... 12 6.2.corbicula as1 Environmental Monitors... .......................... 12 6;3 Bluegill Sunfish as Environmental Monitors.......... ............ 12 6;4 Other Test. Organ $ sus ............................................ 13 6.5 Statistical = Analysis.................... ....................... 13 7.0 IN-RIVER M0NITORINO................................. .............. 13 7.1 Chironomus Sediment Testing...................... .............. 13 7.2 Corbicula as Monitors of Sediment. Conditions.... ................ 13 c 7 3. Invertebrate Monitoring-Stations................................ 13
-7.4: Invertebrate Sample Processing................................... 14 7.5 Invertebrate trJes of Collection. . . . . . . . . . . .:. . . . . . . . . . . . . . . . . . . . . 14 7.6 Aerial Photography. TSS and CT-1 Mesitoring..................... 14 7.7 Efficacy of Molluscicide-Corbicula Control in the Plant. . . . . . . . . . 14 7.8 Overview of Laboratory and In-River Testing...................... 14 l
11
8.0 RESULTS-SUMMER STUDY............................................ . 17 8.1 Ceriodaphnia dubia and Fathead Minnow Reference Toxicant Tests 17 8.2 Ceriodaphnia dubia Survival tnd Reproduction. . . . . . . . . . . . . . . . . . 17
- 8. 3 - Fathead Minnow Survival and Growth. . . . . . . . . . . . . . . . . . . . . . . . . . . . 17 s .4 Chironomus Survival and Crowth in Artificial Streams and River Sediment.............................................. 17 8.5 Corbicula Survival and Growth in Artificial Streame and in River Sediment........................................... 23 8.6 Survival and/or Growth of Selected Organisms in Laboratory Artificial Streace......................................... 23 8.7 Macroinvertebrate Monitoring in the Ohio River................ 30 ,
8.8 Efficacy of Melluscicide-Corbicula Cont ol in the Plant....... 33 8.9 Monitoring of Total Suspended Solids during In-plant Dosing. . . 39 8.10* Aerial Reconnaissance of TSS Levels in the River............ 39 9.0 RESULTS - FALL STUDY............................................. 42
?.1 Ceri ed apba d - dubia and Fathead minnow Reference Toxicant ~
Tents................................................'...... 42 9.2 Ceriodaphnia dubia Survival and Reproduction. . . . . . ........... 42
- 9. 3 Fathead Mipnow Survival and br owth. . . . . . . . . . . . . . . . . . . . . . . . . . . . 46 9.4 Chironomus Survival and Growth in Artificial Streams and River Bediments............................................ 46 9.5 Corbicula Survival' and crowth in Artificial Strer:c and River Sed 1monts............................................ 46 9.6 Survival and/or Growth of Selected Organisms in Laboratory -
Artificial Stresma......................................... 53 9.7 Macroinvertebrate Monitoring in the Ohio River............... 53 9.8 Efficacy of Molluscicide
,,Corbicula control in the Plant. . . . . 53 9.9 Monitoring of Total Suspended Solids during In-Plant Dosing...................................................... 63 10.0 DISCUSSION............................ .................. ....... 63
+ 18.1 Ceriodaphnia dubia Survival and Reproduction. . . . . . . . . . . . . . . . . 63 13.2 Fathead Miunow Survival and 0rowth. . . . . . . . . . . . . . . . . . . . . . . . . . . 67
- 10. 3 ,Ch i r onomus Survi val and 0rowth . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 67
- 19. 4 Co rb i cul a Growth Rat na . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 68 18.5 Advantages of-an On-Site, Erperimental Stream Laboratory..... 68 10.6 - Invertebrate Survival in Artificial Streams. . . . . . . . . . . . , . . . . . 69 18.7 Macroinvertebrate Monitoring in the Ohio River.............. 70 18.8 Foam Production in Efflucnt and CT-1:DT-1 Totals............ 70
- 10. 9 Clan Control during Summer and Fall Dosing. . . . . . . . . . . . . . . . . . 70 11.0
SUMMARY
- 1991 SUMMER.AND ?ALL. STUDIES........................... 71 1 1.1 Summe r Do s ing S tu dy . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 71 11.2 Fall Dosing Study........................................... 72 12.0 LITERATURE CITED................................................. 73 iii
. . . . . . - , , _ . - . ~ . _ _ . . - . ._ .. . . .
iIti t
^
j I l 43.0 AP P LYD I C ES ( "I .- I I ) . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 75 T 13.1 APPENDIX 1I Chio? River Water and Effluent Sampling-Receiving Dates ' V
'~
,and T*st.L Initiation:
13.2 APPENDII II Reference lToxican'; Tests 13.3 APPENDII III Ceriodaphnia dubia 7-Day Tests during Plant Dosing and a LPost-Plant Dosing.(Survival-and Reproduction) t 3.4 APP *:NDII-IV Fathead Minnow 7-Day Tests -(Survival and Growth).
~ 13.:i.- APPENDII - Y Chironomus Survival and Growth in Artifivial Stremns' anu River. Sediment-13.6 APPENDII VI- Corbicuir Curvival and Growth in Artificial Streams and
, , _ . . River Sediments-i% - 13.7 APPENDII' VII Bluegill . Survival and Growth ' in : Laboratory Artificial , io Streams-L13.8 APPEND!I - VIII . Systematic List -- of - Macroinvertebrates Collected in - the Ohio River during the Summer and Fall 1991 Dosing Studies 13.9 APPENDII.II Aerial Reconnaissance of TSS Levels in the Ohio River = 4
,A .
b f
+
iv L . _ , , ,
EXECUTIVE
SUMMARY
Permission was granted by the Pennsylvania Department of Environmental ? Resources (DER) to use a chemical additive (Clam-Trol or CT-1 ) in combination with a detoxification agent (DT-1), a bentonite clay, in the Beaver Valley Power Station Units 1 and 2 river w.ter systems in 1990 and 1991. Reasons for the use of the molluscicide CT-1 in the water systems include the proliferatien of Asiatic clam (Corbicula) densities within the plant and cooling towers, intrusion into and clogging of heat exchangers, and the need to develop an effective biofouling ' control system to counteract the invasion of the migrating Zebra rirsel (Dreissena . polymorpha) which is near in proximity (Great Lakes). The Nuclent Regulatory Commission (NRC) advocates the development of an antibiofouling program by the nuclear power industry which must be maintained in safe operating condition. In accordance with permission granted by the DER and their recommendations after review of the 1990 report, two specific research studies were conductad in 1991: a summer dosing study which continued for 40 days after CT-1 application, and a fall dosing study of similar dur ation. The attached comprehensive report encompasses the data and results of the 1991 summer and fall studies. The 1990 baseline, summer and fall studies were previously submitted on February 25, 1991. l To assure ecological integrity of the Ohio River receiving system during ' the chemical dosing process in 1991, a diversity of toxicological, ecological, and physiological tests were conducted. Teste species included invertebrates and vartebrates. The invertebrates tested included daphnida (Ceriodaphnia dubia) , that reside in the water column, and clama (Corbicula fluminea), snails (Geniobasis sp.) ] and midges (Chironomus riparius) thgt inhabit the river I codiments. The fathead minnow (Pimephales premolas) and the bluegill sunfish (Lepomis macrochirus)-were the vertebrate species tested. In short, a multi-species approach was adopted. A three-tiered approach was employed which included formal laboratory toxicity testing at Virginia Tech (acute toxicity and ?-day survival-impairment);
- r. m-site experimental stream facility which provided greater environmental c W !sm than -formal laboratory testing; and biosurveys (benthic macroinver-
.eb ri.t e s ) carried out in the river. These tests have been developed and/or unworsed by the US EFA and ASTM and are state-of-the-art ecotoxicological protocol.
Summer Dosing Study On August 21-22, 1991, Unit 2 was dosed with CT-1:DT-1 for ~18 hrs to control Corbicula infestation. Ceriodatshnia suffered no significant mortality or reproductive impairment until erposed to 40% effluent while fathead minnow had no deleterious effects through 100% dosed effluent. ~ The fathead minnow had no significant mortality or growth impairment at any effluent concentration including 100%. The US EPA becomes concerned wheti the- impairment effects concentration equals or comes close to the Ohio River instream vaste
' concentration (IWC). In this caso, the BVPS IWC was 5% which is 8 fold lower than the 40% effluent concentraticn found for the most sensitive of the two species tested.
Additional t* sting after the effluent was purged of chemical additives v m
-showed that Chio River water and BVPS effluent did not impair Ceriedachnia reproduction or fathead minnow and bluegill sunfish growth even at 100". concentration of the effluent. Data on the chemical additives in the effluent showed no significant growth impairment for bluegill sunfish. Clam and snail survival in effluent-dosed experimental streams was not significantly different from the control streams.
-Chironomus and Corbicula growth -in the sediment at the first two stations in the river receiving zone was uignificantly reduced after in-plant doeing when compar ed to growth observed at the intake station above the discharge. This effect was observed through the fortieth day. Additional testing was developed in the fall to determine the potential for recovery prior to the fall dosing of the plant.
Benthic macroinvertebrate surveys showed that diversity indices were not substantially differest between stations and dates analyzed. Foam generation during the 1991 summer application was ccatrolled through the use of. a multiple sprayer-j et system within the effluent channel. A double boom containment system in the immediate outfall prevented residual foam from passing further. Juvenile and adult clams held in live boxes during the summer chemical additive period experienced 188% mortality within the first 5 days. River rater temperatures were ~23 C during dosing and as ~high as 26 C within the 100% effluent stream. In accordance with DER's 1991 approval letter dated 4/10/91, aerial plume observations were conducted using still photography (see section 8.10 and APPENDIX II). Fall Dosinz Study On December 18-11 1991 Unit 1' was dosed with CT-1 :DT-1 for ~18 hrs to control Corbicula infestation. Ceriodachnia sufferqd no significant mortality or reproductive impairment at the IWC and in effluent 35 days after in-plant dosing,
~
They had the greatest reproductive success at 198% effluent. Fathead minnow survival and weight gain were not impaired at the IWC. Chironomus survival and growth in the river sediments recovered from the summer dosing and was not significantly impaired before, during or after the - plant dosing in December 1991. The on-site laboratory artificial stream studies added more credence to the studies by- including thermal addition into the stream systems. Asiatic clam, snail a.nd bluegill sunfish survival was basically the same at 8 5. Se and t ee% effluent-treated streams and clam-bluegill growth w..a significantly enriched in 100% effluent. Benthic macroinvertebrate surveys showed that abundance, richness and diversity indices were a function of the sediment type and were not appreciably different between stations. The multiple sprayer-jet syscem used in the summer was equally effective for controlling foam in December 1991. vi
The mo11usc1 cide efficacy for juvenile and adult clam control in Unt 1 Cooling Tower during the fall dosing was not as good as that observed during the summer. Instead of the desired 100% control rate, 43 and 87% of the adult and
. j uvenile clams died. . Cooler river temper.itures and a slightly lesser amount of CT-1 used were contributing factors. No CT-1 was detected in the effluent throughout the dosing procedures.
Immediately after the December 10-11, 1991 dosing of the plant and 35 days later (by January 15, 1992). no acute or chronic effects on the organisms were observed. This included no adverse effects upon survival of Ceriodaphnia, fathead minnows, bluegill sunfish, snails, midges, clams. or on the assemblages i of macroinvertebrates in the river sediment. In addition, Ceriodaphnia I reproduction and growth of fathead minnows, bluegill sunfish and Asiatic clams vere not impaired as addressed by a variety of testing procedures in a formal laboratory, site-specific artificial stream system, and in the river sediments. , l e* vii
1.0 INTRODUCTION
1.1 Overview a.
. Permission has been granted from the Pennsylvania Department of Environmental Resources (DER) to use a chemical additive (Clam-Trol or CT-1 ) in the Beaver Valley Power Station (B7PS) river water systems in 1991. Reasons. for the _ use of the molluscicf de CT-1 in the water systems include the prollferatfon of Asiatic clam (Corbicula) densities within the plant and cooling towers.
intrusion and clogging of heat exchangers, and the need to develop an effective biofouling ' control system to counteract the invasion of the migrating Zebra must.el (Dreissena polymorpha) which is near in proximity (0 eat Lakes). The Nuclear. Regulatory Commission (NRC) advocates the development of an antibiofouling program by the nuclear power industry which must be uintained in sr.fe, operating condition. The purpose of this, report'is to present the results from actual dortng of the . plant with CT-1 for clam control during the summer and fall of 1991. The results of the 24-br. in-plant dosing with an evaluation of molluscicide fate and H offects over 35-4e days thereafter are also presented. This is the second year in which the plant has been dosed for Asiatic clam control. In 199#, . two CT-1 cpplications were made, one in Jw2e and the other in November.
- l. ,
A three-tiered approach was employed which included formal laboratory toxicity testing at Virginia Tech, an on-site experimental stream f acility, and biosurveys carried out in the Ohio River. A detailed description of these strategies, is found in' the previous annual report by Cherry et al. (1991) which was released in February 1991. . 1.2 Toxicity Testing and F.sta/ Effects Strategy The s tat e-of. .the-ar t testing for effluent ramifications into aquatic receiving systems utilized in this project includes a combination of laboratory toxicity testing. an on-site experimental stream system, and in-river validation
. study. These three approaches were carried out concurrently.
The laboratory studies included 7-day survival / impairment testing of daphnida (Ceriodaphnia dubis) and fathead minnow (Pimephales promelas). 10-day Murvival / growth ' impairment of midges (Chironomus riparius). and an ant. lysis of chell growth impairment of Asiatic clama. The on-site experimental stream systems (12 streams) received a river water-effluent ratio in triplicate of 128-e. 95-5. 59-50 and e-100%. The streams were used to valuate survival and growth of Corbicula. survival 4 .d weight impairment of Chirotomus. 35-49-day survival of snails (coniobasis). and 35 day survival and growth of bluegill sunfish (Lepomis macrochirus). In-river studies included invertebrate surveys by penar dredge at a campling station above the plant and 'in three stations below it. Invertebrate curveys were taken before, within 4 and ~40 days after CT-1 dosing. Corbicula Eurvival and growth impairment were evaluated at one upstream and three
, downstacam stations. Chironomus survival and weight impairment were evaluated at these four sta61ons relative to the condition of the deeper river wanthos with 1
c, _ . _ _ ., - at ' freshly deposited sedir 4t during the 33-40-day period following CT-1 desing.
- 1. 3 . Plant Locction BVPS 's-i located in the Borou/;h of Shippingport, Beaver Cc.,an t y . .
Pennsylvania, on a $51-acre tract of land. 1.4- Receiving Water Body BVPS discharges into the Ohio River at river mile 35.0, at a location on the New Cumberland = Fool that is - 5.3. river miles (5.3 km) . downstream fr om
' Montgomery Lock and Dam and 19.4 miles . ( 31.2 . km) upstream from New Cwnberland Lock and Dam.
1.5 19 sting Laboratories Dr. Donald S. Cherry Department of. Biology and University Centan for Environmental and Hazardous Materials Studies Virginia Polytechnic Institute and State University Blacksburg,'YA'24861 (783)_231-6766 Mr. J. Wayne McIntire Environmental Se'rvices Duquesne-Light Company ,
' Beaver Valley Power Station -
P. O. Box 4 . ShippiLvort, PA 15877 (412) 393-5873 l Mr. Robert L. Shema Aquatic ~ Systems Corporation
- 88. Union Avenue ~
- -Pittsburgh,.PA 15282-(412) 367-1989 2.0- PLANT OPERATIONS
- 2.1- Products
. Electrical power
~
2.2 Volume of Waste Flow 48 MGD (million-gallons per day', two-unit operation).
-3;8 SOURCE OF EFFLUENT AND DILUTION WATER-
-3.1 Effluent samples-
, , a. Effluent . Sampling Point I From a pump placed in.the effluent raceway at the point just 2
I l prior to disebarge into the river. l
- b. Collection Dates and Times ( APPENDIX I)
August 20, 21, 22, 25, 1991 (first in-plant dosing phase). Decen.ber 10.11,14,1991 (second in-plant dosing phase).
- c. Cample Collection Method Grab samples taken directly from a boa *.
- d. Streamflow at a time of sampling The river was in a low-flow, clear-water condition during the summer study and moderately so in the fall.
4.0- TEST MFTHODS AT VIRGINIA TECH 4.1 Ceriocaphnia dubia and Fathead Minnow 48-br Acute Toxicity Tests. 4.1.1 Test Methods Used US EPA Methods (EPA /600/4-85/013) by Peltier and Veber (1985). 4.1.2 Endpoints of Test
' Mortality af ter 48 hr and 48-br LQs ( APPENDIX II).
4.1.3 Details of Test Tests were suspended due to data generated in 1990 and ' the 7-day survival / reproduction-growth impairment was used instead. 4.2 Ceriedannnia dubia Survival and Reproduction 4.2.1 Test Methods Used US EPA . Method 1982.0, Ceriodaphnia Survival and Reproduction Test (US EPA 1989).
-4.2.2 Endpoints of Test Seven-day survival and reproductive performance (measured as the
. number of progeny per female) - of the. original orgruisms (APPENDIX III).
4.2.3 Purther Description of Testing Protocol At several points, the US EP A test method offers a choice among various options. The options chosen for the tests are set forth below. In addition. Virginia ' lech . employs certain standard improvements to the US EPA protocol which were used here. These are set forth below. 7.9 Test vessels: 58-mL glass beakers filled with 20 mL of test solution were vied. Better field of view is provided than the recommended 38-mL beakers that have a deeper water column. 7.10.6 Feeding Eelanger et al. (1989) and Belanger and Cherry (1998).have shown that a mixed diet of three green algal spec 4es 3
( Chl amyf omonas reinhardti, Ankistrodesmus falcatus, Chlorella vulsaris) [ termed CAC] increases reproduction and reduces natural variation responses to toxicants. The CAC diet is recommended by these investigators because side-by-side comp ar isons showed CAC to j be superior to yeast-trout chow-Cerophyll (YTC) as food. If CAC is used as food, dissolved orygen depletions are less of a problem. YTC consumes ox7 gen due to the bacterial load whereas algae produce crygen during the 16-br day period. The revised US EPA protocol for l 1989 (US EPA 600/4-89/001) recommends that an algal source be provided. 7.10.12 Because copepods, cladocerans, and rotifers are present in natural waters, all culture waters were filtered through a Vhatman 1.6 um fil'ter to eliminate zooplankton eggs and protozoans. The absence of potential predators and competitors was confirmed by microscopy (zooplankton counts). 11.6 Ceriedaphnia were fed 20 ug algae (dry weight) per container (20 mL) daily. The recommendation of 0.1 mL YCT/15 eL lacks quality control (the weight of food present in the set volume is the key factor) and can result in over or under feeding, and/or excessive bacterial proliferation (Belanger e t al. 1989). 4.2.4 Dnte and Time Teste Began ~ August 22, 1991 at 8:00 A.M. and again at 9:00 A.M. on' September 5. ' 1991 for the summer study and in the fall study on December 11 at 11:00 A.M., 17 at 11:00 A.M., 1991 and again on January 14, 1992 at 3:00 P.M.
- 4.2.5 Date and Time Testa Ended August 29, 1991 at 6
- 09 P.'M. and September 12, 1991 at 6: 00 P.M. In the fall study, December 18 at 6:40 P.M. and December 20, 1991 at 11:00 A.M. Also on January 21, 1992 at 3: 00 P.M.
4.2.6 Type of Test Chambers Pyrex beakerte, 50 mL graduated by 10 mL. 4.2.7 Volume of Test Solution per Chamber 20 mL. 4.2.8 Number of Organisms per Chamber One. I 4.2.9 Number of Replicate Test Chambers per Treatment j Ten. I l l 4 ! k
. _ . _ . _. m _ _ - . . _ - . _ - . ,
L. s i 1
,) 1
.'4!2'.18_ Acclimation of Test Organisms 3 ..-
? Acclimation .. began ony July - 3. - 1991 using females producing in the z third.- brood ~ - - Ohio 1 River water was used-for batch culture and . to f accli'nate ,C. dubia in 1-L pyrex beakers in quadruplicate.
4
.4.2.11; Test Temperature 2 5,+ 1 ' C .
"4.3' Fathead Minnow Survival and' Growth 4.3.11 Test Method Used ~
' US EPA Method '1988.8 . Fathead Minnow Survival and Growth Test.
f 4.3.2 Endpoints of Test . ,
. Seveniday survival - shd ' final.' weight of the test organisms and j measur'ed as _mg/ surviving fian ( APPENDII IV).
- m 1 _
4.3 Further_ Description .cf Testing Protocol ' At1 severalo points, . the - US = EPA' - test (1989) method offers a choice-e among- Various options. - ; The options Jehosen for the -- tests - are set forth below. JIn addition.a Virginit Tech employs . certain standard improvements to'the UB EPA protocol -which were used here. These are ~
= set.forth below.- . .
~tu 6.1 : L Fathead c minnow ' larvae -- are culture- trom in-house- stock 'at
- Virginia Tech. . The condition of ~ eggs ahd . newly - hatched larvae are optimally = controlled only - frou in-house ~ stock? Newly hatched larvae can be 7 shipped in~ 1 well cuygenated water in inat . .ted - containers; however, potential -stress from - temperature and-oxygen shifts during transportation can occur. .. Also, k .owledge of pathogenic stress from fa f fungi-L andE other = disease may . not __ be .: available from fish '. hatchery stock.c Hence. the most ivigorous stock of test fish ~ are those kept-
. ' completely;in^ house.
7 , s 6.8 n The test vessels used were . See : mL (solutica depth-' of 3.6 cm. surface. diameter of o 9.6 cm) instead of 1.8 L to c hance feeding. efficiencies - by!J fish" larvae on brine . shrimp without ' unnecessary *
-overcrowding.
7.11 '. The ' UD EPA protocol recomunends the' use- of larvae that are less
^
'than -24 hr. old. A toxicological - concern is that no -specific procedure. is allotted for. : the removal of approximately 8-11 hr - old _
larvae versus those that are 12 hr : cid. Having an . in-stock collection where thousands of ' . eggs -. can ' be ' available . daily allows
- selection of ; more vigorous larvae- that are closer to - the 12-24 hr 0 iold and not 8-11 hr ' old. Therefore, the bias of natural post-hatch mortality during the first ueveral hours of life is removed.
111.'7.1 Test solutions .were 258 -mL hoased in a 300 mL container. The E- , 5 s
?
,:q, c
) , , _ _ . - - , , , - - M, v VT -M'+ + - * " ' ' '
smal3er volume ' allows greater contact time for fish larvae with their food source. The US EPA (1989) protocol allows for using test beakers from 220 to 1.000 mL. 11.10.1 Fish were dried at 60 C so that lipids would not be volati-lized and lost in the weight determinations. The lower temperature does ' not harm the sensitivity of the test and preserves lipid stores. 4.3.4 Date and Time Teste Began August 22, 1991 at 18:00 A.M. and December 11, 1991 at 11:00 A.M. 4.3.5 Date and Time Teste Ended-August 29, 1991 at 12:08 P.M. and December 18, 1991 at 11:00 A.M. 4.3.6 Type of Test Chambers 598 mL, Pyren 4.3.7 Volume'o.* Teet Solution per Chamber 250 mL. , 4.3.8 Number of Test Organisms per Chamber Ten. , 4.3.9 Number of Replicate Test Chamberg per Treatment Four. 4.3.18 Test Temperature 25+1 C. t l 4.4 Ceriodachnia dubia Culturing 4.4.1 Age 16-28 hrs old at test initiation. 4.4.2 Life Stage First in-star neonate. 4.4.3 Mean Length and Weight Not applicable.
, 4.4.4 Source Duluth, Minnesota, US EPA Environmental Research Laboratory courtesy l
l 6 I
.3 A>
G nh3 - o I
-of Dr. T. J. Norberg-King (7/26/90).
4.4.5 Diseases'and Treatment k Disease free cultures. 4.5_ Fathead Minnow (Pimephales promelas) Ct1turing 4.5.1 Age 24 hrs old at test initiation. 4.5.2 Life Stage 4 Larval, pric' to complete yolk-sac absorption. i
-4.5.5 Mean Weight l i
9.87 ag/ fish; n=20. 4.5.4 Source . In-house cultures or'iginally from Kurtz's Fish Hatchery, Elverson. Pennsylvania'(June 1985). 4.5.5 Diseases and Treatment Disease frdre stock and test animals. 4.6 Chironomus risarius Ten-Day Sediment Survival and Growth 4.6.1 Laboratory Culturing 7-' The Virginia- Tech C. riparius midge larvae were obtained from
. cultures kept I at the Ecosystem Simule**on Laboratory (ESL).
Dechlorinated laboratory : water was used in the cultures while filtered Ohio River water war used for the bioassays. Rearing methods are based on -those descrioed by Nelson et al. (1988), and
'01esy et al. (1988). - Cultures were kept in 28-L glass aquaria on ground paper tovcis and: fed 0.4 g ground Tetraniu fish food daily.
Both culture and testing ' temperatures'were maintained at 28.t2 C. 4.6.3 Bediment Collection Ohio River sediments were collected by ponar grab from one upstream (In or Pumphouse), and, three downstream (P5, 2B and Pie) stations (Fig. 1). .Immediately upon collectien, the sediment samples were placed in polyethylene bags and transported on ice back to the laboratory where they were held at 4 C until the start of the test, a.6.3 Test Protocol The bicassays were initistad with second instar larvae which were {- isolated by first placing fresh egg masses into Se-mL beakers-7
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.8
( containing Chio River water. As the eggs hatched, larvae were cellected and transferred into 400-mL Pyrex containers which contained 250 mL of river water and ground paper towels. Larvae were fr d a 0.1 g/mL suspension of Tetramin fish food daily (Lee et al. 1980), and maintained in the rearing chambers until reaching second instar. Identification of larvae instar was based on head capsule width (second instar larvae were identified as those with a head capsule width of 0.2 to 0.3 mm. J. Tavanaugh, Biology Dept., Virginia Tech. BlacLaburg. V A . , p e r s . c omm . ) . Pyrex storage containers (430 mL) holding 250 mL of river water and 25 g of river sediment (wet weight) were used as the test chambers. To start a test. 10 midge larvae were pipetted into tach of three replicate test chambers for_ a total of 30 organisms per concentration.
. The larvae were exposed to the river nediments for l'8 days, with 200 mL of the river water renewed in each test container every third day. On day ten, all surviving organisms were removed from the test chambers, dried for 24 hours at 60 C, 'and weighed to 0.0001 g on a Cahn electronic balance. The procedure is based in part on methods for Chironomus sp. sediment toxicity tests which are described and reviewed by Giesy et al. (1988), and Nelson et al. (1988). Dis-solved oxygen, pH. conductivity, alkalinity, and har dness were mes.sured for each station at the start and end of days 1, 2, 4, 6 . 8 and 10, respectively.
In addition to sedioent testing in the river. nece .netar C. riparius larvae were transported from Virginia Tech to the field laboratory at BVPS where they were placed in artificial streams receiving straight Ohio River water (control), 5. 50 and 10 0 T. effluent. Three replicate strears containing a total of 30 larvae (10/ stream) were used for each treatment level. Exposures were conducted by placing the larvae in 250-mL square nalgene bottles (58mm x 50mm x 110am) which had been modified by replacing .two sides with a Nytex mesh (60 um) to allow water flow through the chambers. These bottles were then .A4spende.1 in the artificial streams until the end of the test at which time all larvae were removed, placed in 70% ethanol and transported back to Virginia Tech for growth analysis as described for the laboratory study (AFPENDII V). 4.6.4 Testing Dates River sediments for the summer study were collected on August 21 a-d
- 25. September 26. November 5 and 25, 199.. The tests using the August 21 and 23 samples were started together on September 8 1991 while the other tests were initiated on October 7 November 7 and December 6, 1991, respectively.
River sediments for the winter study were collected on December 9, 1991 with the test started on December 12. 1991 while those for the second test were collected on December it. 1991 and that test started on December 12, 1991 as well. River sediments for the 35-day post-dosing test were collected on January 13, 1992 and the test l 9 l
started on January 16, 1992. Artificial stream sediments wtre collected on January 13, 1992 and the test began on January 16 1992 as well. 4.6.5 Statistics The chironomid growth data were analyzed with the Kruskal-Wallis procedure (Hollander and Wolfe 1973). followed .by multiple co= par ison with a rank version of Fisher's frotected LSD (NPSP 1989). 5.0 QUALITY ASSURANCE 5.1 Ceriodaphnia dubia 5.1.1 Standard Toxicant Cadmium atomic absorption spectrophotometry standard. Fisher Chemicals No. S0-C-118 Lot No. 878113-24. 5.1.2 Dilution Vater Used Two dilution waters were used, moderately har d water (EPA), and river water filtered through a Whatman No. 934-AH (1.6 um) filter (Ohio). 5.1 3 Date and Time of Reference Tests April 19, 1991 at 12:30 P.M (EPA), May 17 at 3: 15 P.M. (EPA), May 30 at 11: 39 A.M. (EPA), June 14 at 3:38 P.M. (EPA), July 28 at 5: 00 P.M. (EPA), August 16 at 2:00 P M. (EPA), August 23 at 2:30 P M. (Oh!o), September 19 at 12:30 P.M. (EPA), November 6 at 5:30 P.M. (Ohio), November 11 at 5:38 P.M. (I?A), November 11 at 6: 08 P.M. (Ohio), November 25 at 4:30 P.M. (Ohio). December 19 at 4:09 ( EP A ) . December 19 at 4:30 P.M. (Ohio), January 21, 1992 at 2:00 P.M. (EPA), January 21 ' at 3:08 P.M. (Ohio), and January 25 at 5: 00 P.M. (EPA and Ohio). 5.1.4 Reference Toxicant Results The 48hr Lqs for Cd to C. dubia in EPA moderately hard water was calculated to be 6.93 ua/L on April 18-12, 1991, 31.98 ug/L on May 17-19, 1991, 24.18 ug/L on May 30 1991, 34.4e ug/L on June 14-16, 1991 23.38 ug/L on July 28-30, and 21.02 ug/L on August 16-18, 1991, 13.61 ug/L on September 17-19, 9.48 ug/L on November 11-13, , 10.75 ug/L on December 19-21 and 5.85 ug/L on January 25-27, 1992. The 48hr LQs for Cd to C. dubia in Ohio River water was calculated to be 129 53 ug/L on August 23, 1991, 38.25 ug/L on November 6-8 53.03 ug/L on November 11-13, 56.32 ug/L on November 25-27, 51.01 ug/L on December 19-21, 29.9 ug/L on January 21-23 and 54.17 ug/L on January 25-27, 1992 (APPENDII II). 10
5.1.5 Physical and Chemical Methods Used , Ceriodaphnia testing included s t andar d physical and chemical analyses of test waters by the following methods (method citation by US EPA [1985] follows in par enthe s e s ): temperature (thermometric Method 170.1), conductance (specific conductance Method 120.1 YS1 Model 33), total hardnes s (EDTA titrimetric Method 130.2), total alkalinity (titrimetric Method 310.1 ), dissolved orygen (membrane electrode Method 368.1, YSI Model 57) and pH (electrometric Method 158.1, Fisher Accumet Model 805). 5.2 Fathead Minnow 5.2.1 Standard Toxicant Cadmium atomic absorption spectrophotometry s t andar d, Fisher Chemicals Co. S0-C-118 Lot No. 870113-24. 5.2.2 Date and Time of Test May 15, 1991 at 2tes P.M. (EPA), June 16 at 2: 30 P.M. (EPA), June 24 at 4:45 P.M. (EPA), July 17 at 3:00 P.M. (EPA), August 4 at 9:30 P .M. , and - August 23 at 7: 38 P.M. (Ohio). September 24 at 7:30 P.M. (EPA), November 25 at 2:00 P.M. (EPA). November 25 at 3:00 P.M. (Ohio), December 17 at 5:08 P.M. (EPA). December 17 at 5:00 P.M. (Ohio), and January 27, 1992 at 3:38 P.M. (EPA). 5.2S3 Dilution Vater Used
- Two dilution waters were used, EPA and Ohio River water, the latter filtered through a Whatman #934-AH (1.6 um) filter.
5.2.4 Reference Toxicant Results The 48hr LC5 , for Cd to the fathead minnow in EPA water on May 15-17 June 16-18 June 24-26, July 17-19, and August 7-9, 1991 was determined to be 33.6, 53.0, 34.2, 48.3 and 49.28 ug/L, respectively. The 48hr LC5g of fathead minnow in Ohio River water on August 23-25, 1991 was determined to be 97.23 ug/L (APPENDII II). The 48hrLC58 for Cd to the fathead minnow in EPA water on September 24-26 November 25-27, December 17-19, 1991 and January 27-29, 1992 was 38.86, 35.78, 61 55, and 22.1 ug/L, respectively. The 48hrLqe for Cd to the fathead minnow in Ohio River water on November 25-27, and December 17-19, 1991 was 159.8 and 214.92 ug/L, respectively. 5.2.5 Physical and Chemical Methods Used Fathead minnow testing included standard physical and chemical analyses of test waters by the following methods (method citation by US EPA [1985] follows in parentheses): temperature (thermometric Method 178.1), conductance (specific conductance Method 126.1, - YSI Model 33), total b'ar dnes s (EDTA titrimetric Method 130.2), total alkalinity (titrimetric ' Method 316.1, dissolved oxygen (membrane electrode Method 368.1), YSI Model 57), and pH (electrometric Method
i l i 150.1 Fisher Accumet Model 805). 6.0 ON-SITE EIPERIPENTAL STREAMS LABORATORY a 6.1 Experimental Streams Design Part of the three-tiered testing program was to develop an experimental
-stream system on site. It was used during the summer and fall in-plant dosing for clam control. A series of oval, paddle-driven streams (12) was designed and housed inside a trailer located adjacent to the effluent outfall into the river.
The design utilizes fiber glas s material for simplifying construction and reducing total costs. Streams were 105x79x21 cm with a capacity of 60 liters. River water from a submersible pump in the Ohio River entered via a set of three headboxes. Gravity provided constant pressure through a headbox drain pipe that led to each of the streams. Drain pipes, constructed with 19-mm. schedule 40 PVC pipe, were fitted with 19-mm straight valves that allowed regulation of water flow 1.o each stream. Inflow rates were checked daily. Effluent from the plume was pumped into one headbox and thei was delivered into three sets of three streams at 5% effluent-95% river water. 58-50% effluent-river water and a third set received 1001 effluent. Ve slao included a fourth set of streams that received 188% river water. River water was pumped from the bottom of a travelling screen well at the pu*nphouse through fire hose line to the on-site laboratory. Separate headboxes above each set of three streams received the river water from which pipe lines entered each stream. Stream water depth was regulated by 19-mm diameter. P,VC standpipes mounted in bulkhead and male CPVC adapters. Current was provided by a series of plexiglass paddle wheela attached to a 10-mm steel rod powered by a 1/4 h.p. continuous-use motor. 6.2 Corbicult as Environmental Monitor s For the summer and fall studies, clams were placed in the river at four stations (In. P5. 2B. and P19 as outlinen in Section 4.6.2) They were kept there for one month and were removed for growth analysis just before and through '30 days after dosing in the plant. Also, adult Corbicula were collected from the cooling tower sediment' and thirty clams were placed in each experimental stream. Analyses to be carried out included survival and growth at 35 days after CT-1:DT-1 [DT-1 denotes bentonite clay used to detoxify the CT-1] exposure. Crowth was determined by measuring the videst width from the umbo to the outer stell edge using Vernier calipers (8.81 sm) ( APPENDII VI). 6.3 Bluegill Sunfish as Envir.onmental Monitors In the summer study, bluegill sunfish were placed in each of the 12 experimental streams. to fish / stream after arrival .. at the laboratory 4 days earlier. In the fall study, bluegill were held in the laboratory for 4 weeks prior to testing. Fish were shipped overnight by air freight from Kurtz Fish Hatchery, Elverton. PA.. The fish were housed in cubic-type containers (300 x
, 150 x 17e mm deep) and fed a Tetra-min and ground trout chow mixture twice daily.
A sample of 20 were weighed ( dry weight) and measured (fork length) prior to addition into the streams. At the end of the test all fish were weighed and 12
measured. Fish lengths were measured immediately af ter sacrificing the organisms in ethanol.~ . Fish weights were obtained after drying the organisms at 68 C for 24 hr (APPENDII VII).
. 6.4 Other Test Organisms Snails (Coniobasis) were introduced into the experin. ental streams just prior to dosing r.nd were monitored for 35 days thereafter. The parameter used was survival. Snails were collected from a small stream in Montgomery County, Virginia, and delivered to the on-site labcratory in less than 24 hrs.
6.5 St'atistical Analysis Survival-impairment was analyzed statistically using the Kruskal-Wall'is Test, a non-parametric one-way analysis of variance rank analogue (Hollander and Wolfe, 1973). Significantly different means were determined by a rank-sign least significast differences procedure ( =0.85), Other statistics.1 tests- used included the Dunnett's Procedure and Steel's Many-One Rank Test for Ceriodaphnis and fathead minnow impairment analysis (US EPA 1989). L 7.8 IN-RIVER MONITORING - l 7.1 Chironemus Sediment Testing The 18-day survival and growth impairment test for C. riparius was used to
-.cvaluate the potential of contaminated river sediment prior to CT-1 dosing in the-plant and immediately after dosing to 35 days later. Five tests (pre-dose, post- -I dose 1 post-dose 2 post-dose 3 and post-dose 4) were carried out and detailn of test procedures are found in Section 4.6.3 of this report ( APPENDII V).
7.2 Corbicula as Monitors of Sediment Conditions Asiatic clams were collected from the Unit 2 Cooling Tower at BVPS and brought to the on-site laboratory .where they ware placed in bags (10 per bag, , three bags per _ station) in four stations of the Ohio River (Fig. 1). The four stations inclu'ed one above the discharge near the pumphouse, and the other three were ~358, 788-and 2886 m into the - discharge channel. The bags contained some '~
. glass beads to serve as ballast to keep the bags anchored within the holding containers - set on top of the river sediment. The containers were ' sunk at a distance of ~18 m from the shoreline with a rope from the bag tied to the bank for support and designation of their location. Growth analysis was conducted cfter'the clame were in the river sediment for 35 days (see section 6.2 for details).
7.3 Invertebrate Monitoring Stations Sediment samples in the river'were collected by using a ponar (9x9 in) dredge dropped by block and tackle from a boat. Collections were taken above BVPS nt river mile 34.5 (1), within the effluent back channel at river mile 35.2 (P5) l and 35.4 (2B), which are 8.2 and 8.4 miles below the effluent release to the I river at rivea mile 35 8 (Fig. 1). A fourth station was located in the main river channel (2A) at river mile 35.4 aljacent to Phillis Island. Three sample replicates were taken in the same area for river mile station 34 5 (1) and 35.4
'(2A) while in the ' effluent back channel, the samples were taken at left, mitidle 13 l'
and right locations across each transect. 7.4 Invertebrate Sample Processing The substrate at each sample was characterized at the time of collection, washed within a US Standard No. 30 sieve, preserved with 10% formalin, and returned to the laboratory of Aquatic Systems Corporation. Macroinvertebrates were sorted from each sample, identified to the lowest possible taxon and counted. Subsampling was used when appropriate according to US EPA (1973) methodologies. Mean densities (numbers /d) for each taxon were calculated for each station. Three taxon diversity indices vill be calculated: Shannon Veiner, evenness and richness (number of taxa). 7.5 Invertebrate Dates of Collection Invertebrate collection dates were August 19, 1991 (just prior to the summer dosing study) August 26, 1991 September 30, 1991 (APPENDII VIII). In the fall, invertebrate collection dates were December 9, 1991 (just prior to dosing). December 12, 1991 and January 15, 1992. 7.6 Aerial Photography, TSS and CT-1 Montoring On July 26 August 21-22 and September 29, 1991, aerial photography was carried out above the BVPS by airplane. Aerial photographs included settings fr ota above, adjacent -to and below the discharge area. Total suspended solids levels were monitored and added onto representative photographs. Within the plant. TSS and CT-1 concentrations were monitored hourly to bi-hourly during August 21-22, 1991. These samples were taken at the intake, plume effluent and auxiliary effluent stations and measurements were car ried out at the environmental laboratory located on site. The DT-1 measurements were obtained as total suspended solids or TSS ( APPENDII II). 7.7 Efficacy of Molluscicide - Corbicula Control in the Plant In the summer and fall, Corbicula residing in the cooling tower or pumphouse basin were collected and placed in live-box chambers that were housed in Units #2 or 1 Cooling Tower basin prior to dosing. Adult (18-14 mm) and juvenile (7-9 mm) clams were placed in the live-boxes for 8.4,6,8,10,12,14.16 and
>16 hrs (left in the tower) and removed to an aquarium (with no molluscicide influence) that was housed in the environmental laboratory at the plant. The cumulative percent mortality was monitored in the uninfluenced river water up to 40 days after molluscicide exposure.
7.8 Overview of I.aboratory and In-River Testing Data have been summarized into-54 tables. A summary of the description for each follows. Survival and reproduction of Ceriodaphnia dubia exposed to BVPS effluent during August 22-29, 1991 (Table 1 ). Survival and reproduction of Ceriedaphnia dubia exposed to DVPS effluent during September 5-12, 1991 (Table 2). 14 l l
Survival and growth of fathead minnow l arvae exposed to BVPS effluent during August 22-29. 1991 (Table 3). Mortality and Growth of the midge af ter an initial exposure to artificial stream sediments (Table 4). Mortality anti growth of the midge after a 10-day crposure to Ohio River sediments in the laboratory at Virginia Tech (Table 5). Means (SD) of Corbicula shell lengths after 35-day erposure to river
. effluent (Table 6).
Means (SD) of Corbicul,a shell lengths after 35 days at stations located at the intake.1988 m. and 2880 m and 4086 m below the plant (Table 7). Percent cumulative mortality for Corbicula bluegill sunfish, and a snail in artificial streams housed at BVPS (Table 8). Mortality and growth of bluegill suntith after an initial exposure to effluent from the in-plant dosing operations (Table 9). . Water quality analysis from the artificial stream system located within the Duquesne Light Company's environmental laboratory along ' with meanut ements from
' the plume effluent (Table 10). '
Densities (#/mI ) per major taxonomic groups for benthic samples collected at BVPS transects durin(g the' summer 1991 doaing study (Table 11 ). Diversity values for benthic macroinvertebrate samples collected in the Ohio River during the BVPS fate and effects summer dosing study (Table 12). Efficacy of molluscicide-Corbicula control in the Cooling Tower #f basin after the summer 199' dosing effort (Table 13). Concentrations of _ CT-1 in the amergency effluent, main effluent and river effluent during in-plant dosing (Table 14). CT-1 and DT-1 feed rates during in-plant dosing on August 21, 1991 (Table
'5). .
Total suspended e' lids levels within the Ohio River during and after dosing of CT-1 DT-1 within the piant at the intake, main effluent and auxiliary effluent stations (Table 16). Total suspended solids levels within selected staticus of the Ohio River before plant dosing. morning just prior to dosing, durin6 dosing, and one day later (Tahle 17). Survival and reproduction of Ceriodaphnia dubia exposed to BVPS effluent dosed with CT-1:DT-1 on December 10-11 1991 (Table 18). Survival and reproduction of Certedaphnia dubia exposed to BVPS effluent collected on December te. 1991 and tested seven days later (Table 19). I j l
5 Surviva1 Land' reproduction of Ceriodaphnia dubia erposed to BVPS effluent 35 days aftier dosing _(Tab? e 28). y Survival and growth; of fathead minnov-(Pimephales promelas) -larvae exposed . to BVPS ef fluent collected ~ on Dacember -- 10-11.- 1991 and tested seven days- later (Table 21 ) ._ . Mortality and = growth ---of the midge (Chironomus riparius) after an initial-- exposure to- artificial stream sediments from the in-plant - desing operations
'(Table 22).
Mortality and grnwth of the . midge (Chironomus riparius) .af ter a 10-day expo;.tre_to Ohio _ River sediments (Table 23). Mortality hand growth _ of the midge (Chironomus riparius) r.f ter a'50-day.
--expos'ure to Ohio River sediments (Table 24).
Means (SE) of Corbicula shell lengths measured initially and 35 days af ter
- exposure to river control. 5, 5e and t ee% effluent (Table 25).
.. Percent . cumulative mortality for the . Asiatic clam (Corbicula), bluegill-sunfish (Lecomis macrochirus), and a . , snail .(Ooniobasis) in artificial streams housed,at BVPS (Table 26). ,' , .
Mortality and growth of bluegill sunfish (Lepomis macrochirus) after an V- initial es posure. to effluent ' from the ~1n-plant liosing operations (Table 27). Vater quality analysis from the _ artificial- stream (8.5.50,18e% effluent) system located within the:BVPS-environmental laboratory-(Teb'le 28). Densities (#/m2 ) per ma,jor taxonomic group for benthic samples collected at
- BVPS transects during - the aquatic' ac,nitoring program in the fall- dosing study (Table 29).
. Diversity = values for benthic macroinvertebrate sampics collected from the Ohio River during the December - 1991 : dosing study _ (Table 38).
Efficacy .of_ molluscicide-Corbicula i control in the Cooling- Tower '#,1 basin: after the fall 1991 - dosing effort . (Table 31 ). Concentrations' of- CT-1 in : the main - effluer.t ' during -in-plant-- dosing - in
-December 1991 (Table- 32).
CT-1 (molluscicide) and DT-1 (bentonite clay) feed rates during in-plant
. dosing on December 18-11 -1991 (Table 33).
L Total ' suspended solids (TSS) levels within the Ohio River before. _ during and - af tern dosing of. CT-1 DT-1 ?- within the plant - from September 29-December 13.
-1991-(Tabic 34).
s e-16 m
)
.I
- _ - - - _ _ _ _ - - _ - _ - _ . _ - _ _ . _ _ _ - - - 1
l 8.0- RESULTS - SUMMER STUDY 8.1 Ceriodaphnia dubia and Fathead Minnow Ref erence Toxicant Tests s-Both test organisms had LC y determinations within acceptable limits (Appendix I). Since the Ohio River was in a semi-drought condition, runoff from landscape was minimal. The LC y for Certedaphnia (129.5 us cd/L) in Ohio River
-water was 6 times higher than that found in US EPA water stock.
For fathead minnow, the LC g in Ohio River water was 97.2 ug Cd/L. and in US EPA water stock culture LCg's at least 54% lower (Appendiz I). Compared to problems in 1998 where the Ohio River water was toxic after heavy precipitation, this was not the caso in August 1991. 8.2 Cers odaphnia _dubia Survival and Reproduction In the effluent test during August 22-29, 1991, Ceriodaphnia survival was not significantly affected at 100% effluent concentration (Table 1). Reproduction was significantly reduced at 40% effluent. Therefore. the NOEC (no-observable-effects-concentration) was 20% effluent,while the LOEC (lowest , observable-effects-concentration) was 40% effluent. In the second test..the NCEC was at ,188% effluent for survival a.nd reproduction. In this test, the average number of neonates (27 3) in 188% effluent was only 4.6 lower than the control (31.9). Considerable recovery pf Ceriodaphnia was noted af ter the effluent with
' nolluscicide was tested again *1 week later (Table 2). Also, no daphnida died in the second test.
8.3 Fathead Minnow Survival and Growth There were no significant differences in survival or weight gain of fish exposed to any effluent concentrations relative to the control responses for the test conducted August 22-29, 1991 (Tables 3). This test had no mortality at any concentration tested, including the control. Veight gain of fish was higher in Ohio River water than in laboratory control water. Also, fish weight gain iscreased as effluent concentration increased.
'8. 4 Chironomus Survival and Growth in Artificial Streams and River Sediment Survival and growth of the Chirocomy midge were not impaired in the artificial streams after initial dosing (Table 4). Mortality was variable, being
>20% in the control and 188% effluent streams and lowest (5%) in the 50% effluent streams. Mean dry weight was lowest in the Se% effluent streams but not significantly so due to the high variability in .seights of midges in all streams.
Prior to plant dosing, midges were exposed to sediments collected from baskets housed on the bottom of the river at four sampling stations. Mortal.ity and mean dry weights were not significantly different from each other at all four stations (Table 5).- Variability between weights of midges at each station was also low (0.012 to 0.848 mg ) . In the post-dosed sediments, midge mortalities were not significantly different from each other but mean dry weights of midges were in the river stations. The upper and lower reference stations (In [ intake) and Pte. respectively). -had the highest weights for midges, were not significAntly - different from each other, but were so when compared to those 17
. - . - . , . _ . ~ . . . ~ . - . - --- . . . . - . . . . . ~ - - - - . . - - . . . - . . - . . -
4 Table 1; Survwal and reproduction (# of neonates in three broods) of CenodaDhnia dubia exposed to Beaver Valley Power Station effluent for a test during August 22 29. 1991 when the plant was dosed with the molluscicide CT 1 DT 1 on Augurt 20 21,1991 Effluent was transferred to tes! , organisms daily during the test and was collected on day 1,2,3 and 6 of the exposure following initial in-plant dosing and conditions thereafter Treatments significantly different from the control are indicated by an astertsk (*) at a -20 05 level , Replicate Effluent Concentration (%) 0- -5 10 20 40 100 100' 100' A .35- 19 25 37 27 9 8 24 B- 28 23 29 32 10 6 5 27 C 32 '32 19 34 14 10 6 26 , D 34 24 23 25 26 0 0 28 l .
.E 32 .33 18 31 24 4 8 '
29 l F 34 ~ 26 29 32- 29 4 0 14
-. G ' 24 '21 '10 13 20 1 6 11 H. -32 25 33 28 27 3 0 29 ,
l' 19- 13 32 31' 20 0 1 31
.J 31 30 32 34 21 - -
15 x 30.1 24 6 25 0 29 7 21.8* 4.1* 38* 23 4 Survival 100 100 100 100 100 90 90 - 100
-(%)
Highest CT 1:DT 1 dosing measured in the effluent, Eifluent before addition of CT-1:DT 1 m 18
Table 2.. Survival and reproduction (# of neonales in three broods) of Cenodaphnia dub /d exp0 Sed to
. Beaver Valley Power Station effluent collected on August 21,22. 23 and 26,1991 and test run on Septemb,,r 5 12, 1991. Diluent was Ohio River Water.
' 'a plicate Emuent Concentration V, 0 20 40 100 A 35 24 33 28 8 38 30 31 29
-C 39 37 34 24 0 37' 24 33 27 E .24 13 23 27 F 28 35 25 - 33 G 31 26 34 29 H 19 25 22 25
-1 36 27 -22 21 J- 32 27 30 30 x- 31 9 26.8 .28.7- 27.3 Survival. (%) 100 100 100 100 4
0 19
, . - s _ ,e- .s v--- . , , , - . . . . - --- , - - ,n- .--,-- - _ _m---_m
_ . . _ _ . . _ - . . m._ _. -_.. .. .. ..__. . . . . - . _._1 _ . . . - . _ . ,_ _ Tabte 3 Survival and growth of fathead m'nnow i fPimephales promelas) larvae exposed to Beaver Valley Power Statio'n effluent for seven days from August 22 29, 1991 Larvae were exposed to etnuent contaming CT-1.DT-1 for i day and to flushing of the molluscicide in the effluent
'for days 2. 3 and 6 thereafter Sample size was four replicates of ten fish each Treatments significantly different from the control are mdicated by an asierisk (*) at s =0 05 level Conc. (%) . Mortality (%) i Growth (mg) S 0.
Lab Control 00 0 680 0 156 0 0 Control . 00 0.784 0 063 5.0 00 0 618 0.024 . 10 0 '0.0 0 756 0 049 20.0 0.0 ' O.786 0 051 40 0 00 0 803 0 073 100 0 00- 0830 0'067 e f i 1 e Y 1 20 l. i-l !- , .~ , . ..- - . .
Table 4 Mortality and growth of the midge (Chironomus ricarius) afier an initial exposure to ariificial stream sedirnents from the in-plant dosing operations Sediment exposures were collected in streams at the field laboratory on August 22,1991 at the end of the in plant dosir.g protOCoI. Stream Mortality (%) n Mean On Weight (mg i SE) Control P.3 3 3 0 301 (0 053) 5% 13 3 3 0 313 (0 081) 50 % 50 2 0 225 (o 102)' 100 % 26 7 3 0 307 (0 021)
' 50% based on only 2 replicates due to leakage of holding container 9
9 M S
^
21
a Table 5- Mortality and growth of the midge (Chironomus nparius) after a 10-day exposure to Ohio River sediments in the laboratory at Virginia Tech Sediments taken from baskets in the river
. were freshly fallen material-Pre-Dosed Sediments Station Mortality (%) n Mean Dry Weight Duncan's Misitiple (mg
- SE) Renge'
- In'(intake) 1. . t 8 0 414 (0 012) A ,-
- P5 17 5A 8 0 452 (0 019) A 28- 14A 7' 0 383 (0 040) A P10 16,1A 8 0.429 (0 029) A Post Dosed Sediments -
- A
. _ in (Intake) 3 75A 8 0 579 (0 018)
PS- 24.7 A . 8 0 278 (0 039) C
-2B- 7SA- 8 0 322 (0.067) BC P10 7.5A 8 0 418 (0 030) AB 40 Days Post Dosed Sediments 6.25A 0 712 (0 026) A in (Intake)- 8 P5 .
8.75A 8- 0.522 (0.022) B _ 28- 13 75A 8 0.571 (0 030) B P10 78.75B - 6' O 406 (0 030) C
' 2B based only on 7 replicates due to predation in the test chamber.
8 Means with the same letter are not significantly different-
- P10 means based only on 6 replicates due to high mortality at that station.
G-22
examined at Stations P5 cnd 2B. Station PS, closest to the immediate discharge, had the significantly lowest weight gain of midges followed by Station 2B. Due to the results obtained in the initial, post-doned sediments, another Chironemus test was run using sediments from the same cages collected 40 day s later (Table 5). This time both midge surviv al and weight impairment were significantly impaired in the Pie station. Also, midge weight was significantly lower in the P5 and 2B stations relative to the control. Due to the proximity of the Pie Station to the main river channel, other factors such as sediment contamination from barge traffic may influence these results. Subsequent testing was developed in the fall to determine the potential for recovery prior to desing the plant. 8.5 Corbicula Survival and crowth in Artificial Streams and River Sediment Corbicula mortality in the artificial stream laboratory was nonexistent in all streans and shell length gain or growth was not significantly different
' between control. 5% effluent and tee % effluent streams (Table 6). Clam growth, however, was significantly different in the 50% effluent stream. Overall, the two highest effluent streams (Se and tee %) had lower clam growth than the e and 5% effluent streams, and the e-5% effluent streams vere consistently similar in growth. It was apparent that clam growth was substantially higher in the crtificial streams than in the river stations (Fig. 2).
In the river staticas, clam growth was consistently high and similar between the reference station (Intake) and Pie (Table 7). Growth in the P5 and 2B stations was significantly lower by 3 to 5 fold compared to the control. Clam mortality was e% in the reference stations and 3.3% in Stations P5 and 2B (Fig. 2). 8.6 Survival and/or Crowth of Selected Organisms in Laboratory Artificial Streams Corbicula mortality was nonexistent throughout the 4e days of exposure while snail mortality was extremely low in all artificial stream esposures (Table 8). Mortality for snails ranged from e-10% in the control streams. Bluegill mortality was low for the first week after plant dosing but increased steadily thereafter in the 5e and 100% effluent streams (Table 8). By day 48.-fish mortality was e tg 18% in control and 5% effluent streams and everaged 36.7 to 4e% (which was significantly high) in the 5e to 100% effluent -streams, Growth ~of - bluegill was measared after 4e days in terms of fork length and weight gain (Table 9). Both growth parameters were not significantly different between control and all effluent streams but in each case, length and -waight gain were highest in the control streams and decreased in order from 5, 50 to 100% effluent streams. In general, high variability in both growth parameters prevented the likelihood of detecting significant differences between each artificial stream exposure. Selected water chemistry measurements taken at various times from August 21, 1991 through September 28, 1991 in the artificial streams are presented in Tcble 10. Temperature between the control and 100% effluent streams varied more than any other parameter even though a water chiller was used to cool the 23
Table 6 Means (SD) of Corbicula shell lengths measured initially and after 35-day exposures to river control 5. 50 and 100o ernuent (n = 10) in eacn of tnree rephcate streams ( A. B. C) Treatment Initial Shell Day 30 Gain in Duncan s Mort length. mm Length, mm Lengtn, mm Multiple * 'o Range' 0% Control 13 24 (0 68) 15 06 (0 56) 181(021) A 0 o 5% Emuent 13 12 (0 76) 15 01 (0 68) 189(016) A 50% Emuent 13 31 (0 75) 14 68 (0 64) 137(021) C 0 100% Etnuent 13 34 (0 69) 14 90 (0 54' 1.56 (0 24) A 0
' Means with the same letter are n signt0cantly different.
4 24
.. . . .-. . . - , . . - . - . - . . . .-. . . . . . . . . - . . ,. ~ ~.
Table 7-- Means (SD) of Corbicula shelllengths measured initially and aner 35 days at stations located - at the intake.1000 m (P5). 2000 m (28) and 4000 m (P10) below the plant.
- . . Treatment .
initial Shell - Day 30 Gain in Duncan's Mort. ,
- Length, mm - i.ength mm . Length, mm. Multiple % 7
( t S0) (
- SD) { i SD) Range' In (Intaken 12.78 (0 45) . 13.64 (0.48) 0 87 (0.52) A 0
'P5' 13 01 (0.67). 13 28 (0.67) 027(022) B 3.3 2 B'. 12.97 (0 SS) 13 13 (0.57) 0.16 (0 14) B 33 P10 12.72 (0 69) 13 47 (0 43) 075(042) A 0 4 ,
- Means with the same letter are not sigmficantly different.
' -8 n = 29 ,
4 4 4 7 4 h t 4 25 4 e -w u v 3 a=--r r w r&
m 3 Qpthiquis Growth in Laboratory Artificial Streams and River Sediments I SHELL LENGTH INCREASE (mm)
./
/
2.5 ' l 2- - -m m 1,6 - - _. 0.6 - / ~' w
-/ -
0
/7- i i i /. /. / >
/<7m/ > > >
/
0% 6% 60 % 10 0 % in P6 28 P10 - ARTIFICIAL STREAM MlVER STATION PERCENT EFFLUXWT REPLICATES - ! CA R B MC Mean and Standard Deviation Data Replicates A, B and C Combined 6 HELL LENGTH INCREASE (mm) 2.5 L
- g. ---:~. _ _ . ...... _ , ...1____...._,
1,6 - -- -
-_ _- -[ __
3
- 0. 6 - - --- -- ---
0-- . . , , . , ,- C , O% 8% 50 % 100 % in P6 28 P10 ARTIFICIAL STREAW PSRCENT EFFLUENT RIVER STATION l l I MUN Fig. 2. Graphics of Corbievf e_ growth in laboratory artificici streams and river sediments in the surnrner study. 26
l Table 8 Percent cumulative mortality for the Asistrc clam (CotDicula), bluegill sun 05h (Lepomis macrochirus), and a snail (Goniobasts)in art:0 cia' streams housed at BVPS Test organisms res0cnses were evaluated aner Au0ust 21.1991 on days 1. 7,15,30 and 40 following CT-1 DT-1 'osing into the plant. Corbicula Blueg.H $unfish Gontebas>s St ation % Mortahty % Mortahty % Mortahty Day 1 Control A 0 0 10 Control B 0 0 0 Control C 0 0 0 Effluent 5% A 0 0 0 Effluent 5% B 0 0 0 Efiluent 5% C 0 0 0 Effluent 50% A 0 0 0 Elnuent 50% B 0 0 0 Effluent 50% C 0 0 0 Effluent 100% A 0 0 0 Ernuent 100% B 0 0 0 Einvent 100% C 0 0 0 c-Day 7 Control A 0 0 10 Control B 0 0 0 Control C 0 0 0 Etnuent 5% A 0 0 0 Effh ent 5% B 0 0 0 Efflueni 5% C 0 0 0 Eff utnt 50% A 0 20 0 3 fR'uent 50% B 0 0 0
-E.filuent 60% C 0 0 0 Effkorw 100% A 0 0 0 fffluent 100% B 0 0 0 EtSuent 100% C 0 0 0 Day 15 Covitrol A 0 0 10 Control B 0 0 - 0 Crsntrol C 0 0 0 Effluent 5% A 0 0 0 Effluent 5% B 0 0 0 Efnuent 5% C 0 0 0 Effluent 50% A 0 10 0 Efnuent 50% B 0 40 0 Effluent 50% C 0 10 0 Effluent 100% A 0 0 0 Etnuent 100% B 0 10 0 Efnuent 100% C 0 20 0 Day 30 Control A 0 to 10 Control B 0 0 0 Control C 0 0 0 Effluent 5% A 0 0 0
. Effluent 5% B r 0 0 Efnuent 5% C 0 0 0 Effluent 50% A 0 10 0 Ernuent 50% B 0 40 20 Eilluent 50% C 0 10 0 Efnuent 100% A 0 0 0 Effluent 100% B 0 to O Effluent 100% C 0 20 0
' Day 40 Cont-N A 0 to 10
' Control B 0 0 0 Control C 0 0 0 Etnuent 5% A 0 0 0 Effluent 5% B 0 0 0 Effluent 5% C 0 0 0 Effluent 50% A 0 30 0 Efnuent 50% B 0 60 20 Effluent 50% C 0 30 0 Effluent 100% A 0 30 0 Effluent 100% B 0 40 0 Effluent 100% C 0 40 0 27
. - . . . _ . . . . - . _. ~. . _ . . . . . . . _ . . _ .._.m.m_. _ _ _ . .
.j l
1 iti i l
- Table 9 Mortality and growth of. bluegill sunfish (Lepomis macrochirus) after an initial exposur_e to effluent from the in clant dosing operations Fish were measured for increase in growth by fork length and dry weight Stream Mean Fork Length Mean Dry Weight n (mm SE) (ma SE) I l
Control 39 30 37 (1 55). 0.1114 (0 023) 5% 30 30 21 (1.36) 0.1081 (0 019)
' 50% 18 29 50 (4 131- 0 951 (0 024). )
100 % - 19 28 31 (3 75) 0 831 (0 018)
' 50% based on only 2 repisca s due to leakage of holding container.
- 4. ,
I r s-
.f a
( i J 28 l' l'
-n _a_.._. -.__u._.
l l 7able 10. Water quality analysts from the artificial stream (O. 5. 50 100'b effluent) system located within the Duauesne Liant Company s environmentallaboratory along with measurements from the plume effluent Samples were taken before and after dosing with molluscicide Date Sample Temp. Diss O' pH Cond Alkal. Hardness and Hour - (C) (mg/L) (umnos/cm) fmg/L) (mg'L) ,
'8/21/91 0% Em 22 9 87 7 10 556 43 220 at. 5% Efn 23 3 85 7 40 592 49 180
=0700 - 50, Efn -23 5 83 7 55 718 53 220 100% Effl -23 4 85 8 01 3025 - -
Plume Em. 26 1 78 8 32 963 79 30C
- 8/21/91 0% Efn 23 9 -
7 30 - - -
.at . 5% Em -23 9 -
7 49 - - - 1940 50% Em 25.1 - 7 73 - - - 100% Em. 26.1 - 8.16 - - - Plume Em 28 6 - 8.36 - - - , 8/22/91 0% Em 22.3 8.3 7 23 601 49 180 , at 5% Em 22.6 84 7.05 615 50 180 0100 50% Em 23 4 81 7.59 777 61 240 100% Em. 24 8 82 7 92 980 - -
. Plume Em. 26 5 8.4 8 21 941 81 326 8/22/91 0*', E m. 26 0 79 7 31' 575 49 200 at 5% Em 26.1 78 7.48 618 50 200 1700 50% Em 27.2 7.8 7 85 774 62 260 100% Em. 28 9 7.5 8.29 961 - -
- Plume Em._ 31,2 76 8 43 987 76 300
~ 8/24/91 0% Em. 25 2 7.9 7 45 573 , 45 220 at 5% Em 25 3 7.9 7 54 618 51 220
.1500 50% Em. 26 1 77 8 01 809 67 280 100% Em. 27 0 76 8 34 1080 - -
Plume EfD 31.1 7.4 8.51 1033 84 360 8/28/91 0% Em. 23 9 7.5 7 60 607 41 200 at 5% Em 24 4 77 7.71 659 52 180 0800 50% Em. - 24 6 76 8.02 828 63 2.40 100% Em. ~ 25.1 7,8 8 31 1045 - - Plume Em. 28.1 7.7 8.44 1066 83 340 9/5/9.1 0 % E m .- 22.6 7.8 7.58 558 48 '160 at' 5% Em. 22.7 79 7.78 583 51 200 0730 50'4 Em, 21.9 8.1 8.08 732 66 240-
* .100% Em. 21.3 8.5 8 35 954 - -
, Plume Em. 23.9 8.5 8.45 955 82 300 9/13/91 0 % E m.. 21.2 - 7.0 7.50 569 45 180
- at - 5% Em 21.3 7.8 7.60 575 45 180
-0745 50% Em.- '22.5 7.9 8.07 806 Eb 260 100% Em. 22.6 8.1 8.32 986 - -
Plume Em. 24.9 8.0 8.42 969 79 360 9/20/91 0% Em. 21.7 .76 7.30 527 46 160 at 5% Em. 21.8 8.1 7.42 533 46 140 0730- 50% Em.. 20.5 8.3 7.59 597 53 180
- 100% Em. 16.5 7.7 8.05 820 - -
Pl"me Em. 15.7 11 2 8.15 821 70 260 9/30/91 - 0% Em. 18 3 8.8 7.39 558 46 180 at' . 5% Em. 18.3 90 7.50 579 46 180 0700- -50% Em. 18.4 8.9 7.95 839 69 240 100% Em. 18.7 90 8.27 1157- - - Plume Em. 21.0 8.8 8 34 1167 94 380 29
effluent. Temperature fluctuated from as little as 1.3 C (9/5/91) to as high as 5.9 C (8/29/91). On one occk.toa. 1007, effluent stream temperature was 5.2 C lower than the control stream (9/20/91). Conductivity, pH, alkalinity, and hardness were elevated in the 100'I. ef fluent stream relative to the control river wa1:er. Dissolved oxygen was consistent in all artificial streams. 8.7 Macroinvertebrate Monitoring in the Ohio River Table 11 presents the benthic data according to major taxonomic groups (#/m2 ) for the benthic samples collected at BVPS transects 1 2A, P5 and 28.
' prior . to (8/19/91 ), four days after (8/26/91) and 48 days after (9/30/91) CT 1 desing. At Station 1. oligochaetes and chironomids were greatest in the 0/26/31 sample. Mollusks were most prevalent in Stations P5-L and P5-R as well as in Stations 2 A- A and 2A-C. The greatest density of mollusks was found in the 9/30/91 sample in Station P5-R. No unusual trends were evident between the three sampling dates for the broad taxonomic groups (Fig. 3).
Number of taxa. Shannon-Veiner Inder, evenness and richness are presented { for each of the pre-and post-dosing samples in Table 12. At the bottom of Table 12 mean statistical indices are presented based on the maximum of the three replicate samples. In general, no single station stood out as being too high or too low in experimental variables regarding number of taxa present. Shannon-Veiner Inder, evenness.or richness ( Fi g's . 4-5). Stations 2A and 2B appeared to have slightly higher data. than Stations 1 and P5 in the 8/19/91 samples. Diversity (Shannon-Weiner Index) tended to increase between the 8/19/91 and 9/38/91 samples at a majority of the. stations sampled. The lowest inder values j
. ( <2.8 ) were fo.md in Stations 1C and P5M while values >3.5 were seen in Stations '
P5R in the 8/26/91 and 9/30/91 samples. 8.8 Efficacy of Molluscicide-Corbicula Control in the Plant l The control or eradication of Cerbleula in the boxes housed within the cooling tower basin '% > highly successful during the summer doeing effort (Table 13). After a total molluscicide exposure of *16 bra to CT-1 of 3.4 to 13.8 ppm. I all clams died within 5 days following exposure and subsequent removal to uninfluenced river water. Both adult and juvenile clams were equally sensitive. Clama exposed for 12 and 14 hrs to CT-1 had some survivors 49 days later. Juveniles esperienced 65-97T. mortality but adults were dead after 5 days. No clams died from the first 8 hre of CT-1 exposure. Maximum CT-1 concentrations within the. plant proper ranged from 8.4-13.5-9.8 ppm between 1888-8288-8438 hrs. The first detectable amount of CT-1 (0.15 ppm) was measured at 1588 hr on August 21, 1991 and the final residual (6.3 ppm) occurred the next day at 1438 hr. No detectable residuals of CT-1 were measured in the main effluent but on three occasions (2288, 2388 and 8888 bra), some CT-1 residuals (B.S. 4.4 and 8 91 ppm) were measured in the auxiliary effluent (Table 14). These positive measurements were attributed to a slug of CT-1 that developed over time in the s.ystem. When it was initially detected, the DT-1 slurry concentration was increased to 42 and 49 ppm at 2315 and 2345 hrs (Table 15). This buildup was a learning experience since Unit 2 had not been dosed before. Corrective actions were taken to prevent this incident from occurring in the future even though the aux 211ary effinnt is considerably lower in volume than the main effluent. , l l The pounds /hr of CT-1 and DT-1 delivered are found in Table 15. The DT-1 ) I l l 20 i
W Table 11-- Densities (ellm') per major taxonomic group benthic samples collected at BVPS transects ; during the aquatic monitoring program just prior (8/19/91) to dosing the plant with CT 1, rive ,
' days later (8/26/91L and 40 days (9'30/911 there after l I
Date - , Taxonomic of BVPS Transects ; Group Collection 1A 1B 1C 2A-A. 2A B 2A C PS-L P5-M P5 R 2BL20M20R Oligochaeta - 8/19/91 3014 1952.1517 118 2187 1024 729 355 2541 1694 20 2838 8/26/91 12410 9063 4491 709 99 749 2424 1517 4096 1831. 78 5042 , 9/30/91. 3566 2759 1735 749 1971 3348 4453 473 7490 60 177 3960 i Chironomidae 8/19/91 354 888 1103 316 3093 571 453 59 1597 336 40 2324 8/26/91' 3940 4374 5437 808 138 1361 1754 354 4373 513 . 0 2522 . 9/30/91 533 198 79 .78 867 1458 1478 493 4728 198 20 2483 Mollusca - 8/19191 59 118 59 532 -769 .453 99 0 2620. 59 39 236 39 158 8/26/91 '749 431 197 -1950 591 '1084 1063 59 3113 236 9/30/91 473 158 .39 .374 768 1891 59 79 5122 138 39 551 . .Others 8/15/51 0 0 20 40 40 0 20 0 39 79 - 40 0 8/26/91 39 118 0 0, 0 20 40 59 315 0 39 0 9/30/91 20 0 20 0 59 60 40 20 1006 158 20 59 D 4 , 31 J.
-e , - ----,,-e ,, , ,, , - - , . . . , , __
BVPS FATE AND EFFECTS SUMMER 1991 STUDY
. BENTHIC SAMPLES - CHIRONOMIDAE DATA NUMBER OF CHIRONOulDS/8QUARE METER
..- 3 . _...... .. _ -..- - . _ - - . -
.._g. -. ..
=.
g E~
~ ~ 'c: ~~~
3000 -
~ ~
2000 - ~ g, g: e., e 1000 - ' C e
,\ ./
%D c:a
/ ] '/ / /'.. / '/
/, f 1A 18 10 2AA 2AB 2AC P8L PSM P5R 28L 28M 28R BVPS TRANSECTS SAMPLING DATE R hg.19,1991 C Aug. 26,1991 E 8ep. 30,1991 BVPS FATE AND EFFECTS SUMMER 1991 STUDY BENTHIC 8AMPLES - OLIGOCHAETA DATA NUMBEM OF OLIGOCHAETES/8QUAME METEM 14,000 - t:1 12,000- -
10,000-8,000- _ E - - 8,000- - . , 4,000 - e, - ,,__ c ,. J J ;Ss 7'~ . w/ 2,000 - _ _ y 5 ,; , _ .
~
0
/
i
'} *) , /w/ -
. f , WM,),-
t rf /1 - i i i i i i , i i i i 1A 18 1C- RA A 2A8 2 AC - P8L P8M P8R 25L 23M 28R BVPS TRANSECTS 8AMPLlHG DATE
. I IAug.19,1991 L_ l Aug. 26,1991 E Sep. 30,1991 Fig. 3. The density of chironomids and oligochaetes for the summer sampling effortin the Ohio River.
32
BVPS FATE AND EFFECTS SUMMER 1991 STUDY TOTAL NUMBER OF TAXA PER BENTHIC SAMPLE NUMBER OF TAXA 60- .
# ~
30- _ 20- V " ar c-
; s[~~ _
- y -
10- c 5 - T'} f'-' ' 'T 9 7
#~~ '
0
' " - ~ '
, i '-'-'7 i 1A 19 1C 2AA 2A8 2AC P5L P8M P8R 2BL 2BM 2BR BVPS TRANSECTS EAMPLING DATE I I Aug.19,1991 L_ J AU9 26,1991 E Sep. 30,1991 BVPS FATE AND EFFECTS SUMMER 1991 STUDY TOTAL NUMBER OF. ORGANISM 8/8OUARE METER HUMBER OF ORGAN 18M8/800ARE METER 20,000 '
__, d c:- 16,000 - "
~
12,000 -
/
P,000 - ~ c, . y #
? c cu C'l
~
b 4,000 - i W/
- ./ x - .
a - 7e 2 0 /-)-) 1 . .
,/
k,- Q , J/, , A, a , , /. /./w/ 7 . i 1A 18 1C 2A A 2A8 2 AC P6L PSM PER 2BL2BM2BR BVPS TRANSECT 8 BAMPLING DATE I I Au9 19,1991 [ 3 Aug. 26,1991 E 8ep. 30,1991 Fig. 4. The number of taxa and density of invertebrates for the surnrner sampling effort in the Onio River. 33
BVPS FATE AND EFFECTS SUMMER 1991 STUDY SHANNON-WEINER INDICES - BENTHIC SAMPLES 8HANNON WEINER INDEX
.. 4 _
_h .. 2.5 - b~ e
; l 2- 2,
~ ~ ~
1.6 - 0.6 - ,, ,, _, _, ,, ,,[ , _, E _ j
/- 7 7 >/, / 7 -- 7 / / - 7.- 7 /, /-s 7(7 1 n
1A 18 1C 2 A A 2 A8 2 AC P6L P6M P6R 28L 28M 28R l l BVPS TRANSECTS l- ; SAMPLING DATE I I Aug.19,1991 M Aug. 26,1991 M sep, so, test BVPS FATE AND EFFECTS SUMMER 1991 STUDY RICHNESS VALUES - BENTHIC 8AMPLES RICHNESS WLUE 6- -, 4 3- c,
~
~#'._
~~ ~
~ ~
7~ Y ; ,~ 0
# T' I' I, ' I' I' ,
' T' T' '- AI '~
1A 18 1C 2AA 2A8 2AC P8L P6M P6R 48L 28M 28R BVPS TRANSECTS BAMPLlHG DATE I i Aug.19,1991 L J Aug. 26,1991 M sea. 30,1991 Fig. 5. Shannon-Weinerindex and richness of invertebratea for the sumn.er sampling effort in the Ohio River. 36
Table 12 Deversity values for benthic mateomvet1etsinte samples t.olletted from the Ohio her durmg the OVPS f ate end e"ects summer 1991 desmg steo, Station Numt er Parameter iA 18 iC 8-.9 8 26 4X RI]6 9 30 $ 19 1 I 9 39 No of Taxa 12 18 17 15 18 14 11 17 12 Shannon-Woner ~u 2.17 2 61 2 66 2 47 1 97 2 35 2 24 1 92
- edex Evenness 0 61 0 52 0 64 0 68 0 59 0 52 0 68 0 55 0 54 Richness 1 35 1 74 1 90 1 75 1 78 1 62 1 27 1 74 1 46 Station Number 2AA 2AB '
2AC 6 19 $ 26 ~7 9 8 19 $$ 9-56 ft 19 B 26 9F L No of Taxa 9 16 11 25 10 14 12 16 17 Shannon-Weiner 2 27 2 88 2 81 3 02 2 20 2 51 2 77 3 10 2 74 index Evenness 0 72 0 72 0 81 0 65 0 66 0 66 0 77' O 78 0 67 Richness 1 16 i 84 1 41 2 75 1 34 i 58 44 i 86 1 61 Station Number P5R P5M P5L 8 19 8 26 9 30 8 19 8 26 9-30 8 19 8'76 9-30__ No. of Taxa 15 20 42 6 10 10 13 18 14 9hannon Welner 2.41 3 53 3 80 1 78 2 47 2 69 2.81 2 86 2.13 Index Evenness 0 62 0 82 0.71 0 69 0 74 0 81 0.76 0 69 0 56 Richness 1,59 2 02 4 18 0 83 1.ie i 29 1.67 i 98 1 49 Station Number 2BR 2BM 2BL 2 8 19 BWTTi 8 19 B-26 9 36 bi9 8 26 9-30 No of Taxa 17 10 21 6 4 8 14 3 1? w.annon-Weiner 3.01 1.04 3 31 2 53 2 00 2 BB 2.50 2 46 2 93 Index Evenness 0 74 0.58 0 75 0 98 1 00 9 96 OSC 0 74 0.85 Richness 1.86 1 01 2.26 1.01 0.59 1 26 1 69 1.15 1.59 Values cattulated for the maximum of three replicate samp n from each station Station Number '~ i P5 2A 2B _8-19 _B-26 9-3D *._19 _8 26 _9 30 8 W_8 _ 2C. _9 7_0 _19 8 26 _9.30 No. of Taxa 20 24 19 /i 28 45 27 21 21 24 15 25 Shannon Weiner 253 241 2.35 #3 349 397 310 311 2 62 3.12 227 351 Index Evenness 0.59 0.53 0.55 061 0.73 072 0.64 0.71 0 64 0.68 058 0.76 Richness 2.37 241 2.23 2.52 3 08 4 BS 337 252 2.42 252 1.72 305 35
l Table 13 EfGcacy of mollu ticide Cort"cuta control in the Coohng Tower #2 basin after the Summer 1991 dosing effort Clams in baskets were enosed to CT.1 for O( A). 4(B). 6(C). 6(DL 10(EL 12[F).14(G)_16(H) and di6(t) his Clam moria fly 15 ItSted by adults (1215 mm) and m parentheses, juvemies (7 9 mm) CT-1 Dosing Clam Mortality (%) Hour Cont (ppm) Day' A B C D E F G H I 1120 <02 1 0 0 0 0 0 0 0 0 0 1300 15 (0) (0) (0) (0) (0) (0) (0) (0) (0) 1400 34 2 0 0 0 0 0 0 0- 0 3 1500 36 (0) (0; (0) (0) (0) (0) (0) (0) (20) 1600 49 3 0 0 0 0 0 0 0 3 90 1700 69 , (0) (0) (0) (0) (0) (17) (17) (7) (57) 1800 84 4 O O O O 7 7 93' 93 97 1900 8.3 (0) (0) (0) (0) (0) (60) (93) (73) (100) 2000 91 5 0 0 0 0 50 100 100 100 100 2100 10 8 (0) (0) (0) (0) (0) (13) (97) (100) (-) 2200 11 4 6 0 0 0 3 57 -- - 2400 12 3 (0) (0) (0) (0) (0) (63) (97) v100 10 9 9 0 0 0 0 60 - - 0200 13 0 (0) (0) (0) (0) (0) (63) (97) 0300 11 6 12 0 0 0 0 60 - - 0430 90 (0) (0) (0) (0) (0) (63) (97) 0500 59 15 0 0 0 0 60 - - 0600 , 5.7 (0) (0) (0) (0) (0) (63) (97) 0700 34 20 0 0 0 0 0 - - 0800 4.7 (0) (0) (0) (0) (0) (63) (97) 0930 10 30 0 0 0 0 0 - - 1200 03 (0) (0) (0) (0) (0) (63) (97) 1430 03 40 0 0 0 0 0 - - 1630 <02 (0) (0) (0) (0) (0) (63) (97)
, ' Day represents time after plant dosing in which clam mortality was observed-1 36
l g l l l Tat'le 14 Concentrations of CT.1 in the auwthafy efUuent. main effluent and river efnuent during ! in plant dosing I Date Auritiary Main River Hour Efnuent (ppm) Ernuent (pom) Efnuent (ppm) 8/21 0930 <2 <2 <2 l 8/21 1000 <2 <2 <2 ' 8/21 1100 <2 <2 <2 ; 8/21 1200 <2 <2 <2 ' 8/21 1300 <2 <2 <2 8/21 1400 <2 <2 <2 8/21 1500 <2 <2 <2 8/21 1600 <2 <2 <2 8/21 1700 <2 <2 <2 8/21 1800 <2 <2 <2 - 8/21 1900 <2 <2 <.2 8/21 2000 <2 <.2 ..2 8/21 2100 <2 <2 <2 8/21 2200 0.5* <2 .- <2 8/21 2300 44* <2 <2 8/22- 0000 0 91* < .2 <.2 8/22 0100 <2 .<2 <2 t 8/22 0200 <2 < .2 <2 8/22' 0300 <.2 <2 <2 B/22 0400 <2 <.2 <.2 8/22- 0500 <2 <2 <2
- See corresponding data in Table 15, 37 t
s.__ .__ ._ _ _.. _ .._- _ . _ _.__ _._. . _ . ~ _ . . . . - - . . - . _ _ _ . _ _ . _ I
. Table 15 CT.1 (molluscicide) and DT.1 (bentonite clay) feed rates durin9 in plant dosing on August 1 21,1991 i 1
Date ' lour CT-1 Slurry Slurry (ppm) DT 1 DT.1 Ratio' ) (Ibs/hr) (Ibs/ht) (lbs/hr) (ppm) DT 1/CT.1 8/21/91 0940 283 9 34 6 1,2/1 69 2_ - l _8/21/91 0943 283.9 69 2 34.6 - - 12/1 ) 8/21/91 0946 283.9 69 2 34 6 276 4 20 6 12/1 i 8/,21/91 1415 283 9 69 2 34 6 2316 17 2 1.1/1 ; 8/21/91 1945 283 9 69 2 34 6 249.5 18 6 i ili : 8/21/91 2045 - [83.9 -69 2 34 6 276 4 20 0 1.2/1 I 8/21/91 2215. 283 9 69 2 34 6 360.1 27.2 1.5/t
-8/21/91 .
,2230 283.9. '69 2 34 6 276.4 20.6 1'2/1 - '-
- 8/21/91 2315 '283 9 84 0 42 0" 276 4 20 6 1.3/1 "
8/21/91 - 2345- 283 9 -103 2 49 0" 276 4 20 6 . -1.3/1
'8/22/91 0200 0 103 2' 49 0" 276 4 20 6 --
8/22/91 0255 0 1012 49 0" ~ 186 7 13.9 - , 8/22/91 0315 0 90- 4.3 186.7 13.9 - 8/22/91 0445 0 00 43 141 9 13 6 - I 8/22/91- 0645 0 0 0 0 0 - i 4
- DT 1 and CT 1 used was 6.487 and 4.643 lbs. respectively for an overall ratio of 14/1. [
" Refers to correspondino data'in Table 14.
-i r
6
-. h t
38 I
. , , . , - - . _ . ~_ ,,...~.m....,__..__._.___m_,. _ . _ , . - . .. - - . . _ - , ,~.. ~._..._.~.-[
in 1bs/hr was weig.hed on a scale, changed into a slurry, and metered out with a conversion from lbs/hr into ppm. The CT-1 metered in was constant at 283.9 Abs /hr through 2345 hr after which it was reduced to 0. The DT-1 slurry produced ranged from 276.4 lbs/hr at 0946 hr to a high of 366.1 lbs/hr at 2215 hr. The DT-1 conversion into ppm ranged from "7.2 to 27.2 ppm during 9/21/91. Overall, the DT-1 addition averaged *20 ppm. The total number of pounds of DT-1 to CT-1 used were 6.487 and 4.643. respectively. This accounted for a final feed ratio of 1.4/1 of DT-1/CT-1. 8.9 Monitoring of Total Suspended Solids during In-plant Dosing The TSS levels measured in the main effluent ranged from $3.6 ppm at 0900 hr (August 21 1991) to 75.0 ppm at 1100 hr on August 22 1991 (Table 16). Although the bentonite clay constituted a certain portion of the effluent TSS. the oxidative action of CT-1 on the slime (1e.. algae. bacteria and fungi) buildup in the tower comprised a substantial part as well. The lesser flow of the auxiliary effluent ranged from 57.0 to 124.5 ppm during dosing. Background TSS concentrations from up river (intake) samples t ak en after dosing at 1400 and 1900 hr ranged from 4.7-6.0 ppm August 22, 1991 (Table 16). Other than one measurement at 12.0 ppm at 0900 hr on August 21 1991 TSS levels were uniformly low in the river. In general. intake TSS levels u7ually r ange d f rom 4.7-7.7 ppm. The rivrr was at its clearest state when compared to previous in-plant dosing efforts. 8.10 Aerial Reconnaissance of TSS Levels in the River On three occasions. TSS serial reconnaissance photographs and river samplings by boat were taken. On July 26, 1991 (Table 17). Intake. P5. 2B and Pte stations had surface measurements that ranged from 4.0 to 7.0 ppm. Bottom water sanples tended to be nearly twice as high in TSS than surface samples. The TSS level in the main effluent was only 7.5 ppm. In the morning just prior to dosing. TSS surface and bottom measurements were quite similar to the previous sampling date in July. The main effluent TSS was 29.2 ppm. at 0800 hr. During dosing, one TSS reading was made (52.0 ppm) at 1400 hr and on the same hour one day later, effluent TSS was reduced to 15.0 ppm. Aerial reonnnaissances were placed in Appendix I and listed as Photographs 1-10. The overview of the plant and receiving wystem in Photograph 1 showed a system with low TSS input (4.0-7.5 ppm at the surface and 9.7-14.7 ppm near the bottom). The closeup of the initial discharge zone indicated that the water was clear in the 5.7 to 11.7 ppm mr.rked areas. The tan, cloudy breas above the discharge were the result of either shallow river cones that are naturally turbid or are caused from river bargr traffic after the waves wash against the river bank. In Photograph 5. the shallow, turbid zone along the river bank extended downstream from the discharge area that was clear. On the day of doming, effluent TSS was photogaphed and measured at 52.0 ppm in Photograph 4. The zone of TBS was extended to the tip of the island and sli6h tly below. The same areas of natural siltation along the shoreline above and below the discharge were evident in Photographs 4 and 5. More importantly. TSS dissipation was markedly reduced from 52.0 to <15.0 ppm by the PS station. During the low river flow conditions on 8/21/91, turbidity appeared to back up the river but did not reach the intake pump station. 39
1 Twe is Total suspended solids (TSS) levels within the Ohio River during and after dosing of CT 1 DT 1 within the plant at the antake main effluent and aumtilary effluent stations Period of in Plant Dosing and TSS fppm) Hour intake TSS Main Effluent TSS Auxiliary Effluent TSS + August 21.1991 , 0800 - 29 2 73 0 : 0900 47 53 6 124 5 1100 7.7 50 0 124 5 1300 7.0 68 0 91.5 1500 63 82 5 86 5 1700 63 53 0 100 0 1900 '67 ,
'50 0 95.5 2300 50 58.5 102.5 2300 5.7 71.5 83.0 August 22,1991 0100 5.0 60.0 84.0 0300 6.7 f,0 0 76.5 0500 . 4.7 52.5 48 0 0700 43 70 0 43 0 0900 12.0 31 0 37.0 1100 47 73.0 16 0 1400 4.7 15.0 12.5 1900 60 17 0 14 0 r
40
I Table 17 Total suspended sohds (TSS in opms levels within selected statrons of the Ohio River before plant desing (7/20'91). morning just prior to cosing (8/21/91-0800 hrl. during dcsing { Bf 21/91 1400 hri, and one day tater (1'22'9114'10 hr) Station 7/26/91 1400 hr 8/21r31-08(O hr 8/2191 1400 hr 8/22/911400 hr Intake surf ace 70 80 63 77 Intake bottom 14 7 15.0 10 0 11 0 PS sudace 57 70 13 0 57 - PS bottom 11 7 23 3 24 7 03 7 2B Surf ace 40 93 93 63 2B bottom 97 12 3 13 7 16 0 P10 surface 50 97 87 67 P10 bottom 14 7 19 0 15 0 15 7 Main effluent 73 29 2 52 0 , 15 0 Auxiliary ernuent - 73 0 105 0 12 5 e p. 41
I Photographs 7-9 show conditions in the river-receiving system for the day after dosing. The TSS levels were similar to those reported en 7/26/91. The same , silty regions were apparent from shallow waters and oscillating waves condit1cns. An additional Photograph (18) was t ak en on 9/29/91 which occurred during very clear '1"er conditions and more than one month af ter in-plant dosing. River turbidity appet Jd high between the pumphouse and discharge ( i e . . TSS wa s 1. 0 and 31.4 ppe. respectively). During this period of low river flow, natural TSS conditions were obvious around the discharge area in Photograph 18. The areas of j turbulence along the river bank were spread across the river to the tip of the ! leland, as well as into the discharge channel toward Station P5. Photograph 10 I resembled Photographs 4-6 taken during in-plant doming even though it was shot one month later. It appears that natural river sedimentation can ar ,s e ar to contribute measurable forms of TSS within the Ohio River during extreme low-flow i conditions b) scouring the shoreline. I 9.0 RESULTS - FALL STUDY 9.1 Ceric. daphnia dubia and Fathead Minnow Reference Tomicant Tests Both test organismo had LC., determinations within acceptable limits (Appendix I). The Ohio River was recovering from a summer-fall drought condition and runoff from the landscape was not substantial. The LCgg ' s for Ceriodaphnia (29 9-56.3 ug cd/L) were several-fold greater than those found in UD EPA water stock. For fatbead minnov, the LC g ,'s in US EPA water stock ranged from 22.t-61 5 ug Cd/L. In the US EPA water stock oulture. LC g ,'s were considerably higher (159.8 214.9 ug cd/L). Compared to probleme in 1998 where the Ohio River water was toxic af ter heavy precipitation, this was not the case in the fall . dosing effort. 9.2 Ceriodaphnia dubia survival and Reproduction In the effluent test during December 14-21, 1991 Ceriodaphnia survival was significantly affected at 28 48 and 188% effluent concentrations (Table 18). Reproduction was significantly impaired at 18-100% effluent. The effluent prior to molluscicide addition also significantly impaired neonate reproduction although 86% of the adults survived. Neither survivorship nor neonate impairment was hampered at the inntream vaste concentration of 5% effluent. Therefore the NOEC was te% effluent for survival and 5% effluent for reproduction. In the second test where the initial effluent was held for 7 days and then tested, all ceriodaphnida died at 48 and 188% effluent (Table 19). It appear ed that the torio constituents did not break down withir 7 days after molluscicide application. After 35 days, the effluent from the plant was collected and tested again for poterc?.ial residual effects from molluscicide application during the previous month. Survival and reproductive success of Ceriodaphnia was not significantly different between control and 100% effluent treatments (Table 20s. In general, reproductive success tended to increase between control and 40-100% effluent crposures while survivorship remained consistent at 100% throughout. 42
Table iP Survival aad reproduction of of neonates in three broods) of Ceriocachne dubia exposed to Beaver Valley Power Station etRuent for a test when the plant Was dosed with the mollusticide Ci 1 DT 1 on Decemtser 10 11. 1991 Ef11uent was transferred to test organisms daily during the test arid was collected en day 1 2. 3 and ti of the exposure following intilal in-plant dosing and conditions thereafter Treatmerits sigtiifttantly different from the control are ind!cated by an asterisk (*) at t =0 05 level Replicate Effluent Contentratico ('s) 0 5 10 20 40 100 100' 100' A 34 25 29 0 0 0 0 5 B 28 33 32 0 0 0 0 13 C 34 29 29 0 0 0 0 4 D 33 30 30 0 0 0 0 3 E 27 31 00 0 0 0 0 2 F 34 26 29 0 0 0 0 0 G 3B 32 28 0 0 0 0 0 H 30 27 27 0 0 0 0 16 1 36 32 23 0 0 0 0 3 J 26 32 16 0 0 0 0 2 x 32 0 30 0 27.3* O' 0' 0' 0' 48' Survival 100 100 100 0* O' 0* O' 80 ( e ) Highest CT 1 DT 1 dosing measured in the effluent.
' Ernuent before addition of CT 1 DT 1.
43
i Table 19 Survival and reproduction te of neonates in three btoods) of Cenodaphnsa cubs 3 esposed to Beaver Valley Power Station effluent collected on December 10 1991 and test run seven days later Diluent was Ohio River Water Day Survival at Emuent Concentration 's of Test 0 40 100' 100' i 100 0 0 50 4 2 100 - - 10 3 100 - - O e Survival ('J.) 100 0 0 0
- Highest CT 1:DT 1 dosing measured in the effluent
' Emuent before addition of ' CT 1 DT-1 44
.- ~, .. - - . . . . . . _ _ _ _ _ . - . - - . . . - _ . . _ - . . . _ . . . -
1 1 Table 20 Survival and ipproduction (d of neonates in three broods) of Cenorf3phnia dubia erposed
- to Beaver Valley Power Station efnuent for a test 35 days after the plant was dosed with the molluscicide CT 1 DT 1 on December 10 11. 1991 Einuent was collected once and 1 transfetted to test orgar"sms daily during the test Treatments signilitantly different from l the control are indicated by an asterisk (*) at i = 0 0$ level '
Replicate Efnuent Concentration (%) 0 5 10 20 40 100 A 21 1? 2B 11 28 25 B 26 24 26 29 31 27 C 13 20 26 32 27 29 D 24 24 29 22 24 21 E 2$ 9 23 21 24 30 F 27 26 2 25 26 27 G 29 23 23 21 24 29 H 26 22 26 18 23 24 1 25 10 25 22 24 23 J. 23 22 21 20 24 22 x 23.9 20 3 22 9 24 2 25.5 2$.7 Survival 100 100 100 100 100 100 (%)- 1 45-
9.3 fathead Minnow Survival and Crowth Fathead minnow survival was not significant between 0 through 100% effluent since no fish died in the test (Table 21). Fish growth was high and ranged from 0.902 mg in the control to a lov of 0.703 mg at 100% effluent. Although scme fish impairment was noted at various effluent concentrations and then not at others, the inconsistency in the fish weight was not ecologically significant. The weight gain of fish at 0.7 to 9.9 mg was exceptionally high throughout the test while the variance (standard deviation of fish weights) was unusually tight. The NOEC for fish survival was > 10 0% effluent and depending upon the interpretation of the data, the NOEC for growth could be 5 or 100% effluent. In either case, the IVC was not violated in terms of fish survival or weight gain. 9.4 Chironomus Survival and Crowth in Artificial Streams and River Sediments Survival and growth of the Chironomus midge were not impaired in the artificial streams 34 days af ter molluscicide treatment in the pi.ent (Table 22). Midge mortality was low throughout (ie. , 3 5 16.7%) and midge growth was highest in the 100% effluent streams than anywhere else. Prict to plant dosing, sediments were taken from the river in baskets held at the bottom, and then returned to the laboratory for midge survival / impairment consequences. Erperiments began on a/21/91 and continued several times thereafter (ie., 0/23/91, 9/26/91, 11/5/91 12/9/91, 12/11/91 and 1/13/92) to study the trends in midge survivorship and growth throughout that time (Table 23). Before plant dosing on 8/21/91, midge survivorship and weight were genere11s the same at all sampling stations. After,the summer dosieg, significant differences in weight impairment were observed (Tables 5. 23 and 24), so these concerns were monitored at more frequent intervals thereafter. Midge survival and growth appeared to stabilize by the 11/5/91 sediment sampling but deteriorated somewhat in the 11/25/91 sample. The major problem o; curred between the pumphouse and P18 Station, that is, the station furthest away, below the island which can be influenced by mainstream river barge traffic. River sediment samples collected in 12/9/91 (before in-plant dosing) and 12/11/91 (shortly after in-plant dosing) showed no significant mortality or weight impairment between upstream (pumphouse) and dovnetream stations (Table 24). Approximately 35 days follovira molluscicide exposure, midge survival and weight were not significantly different between stations, and when considering weight, the upstream station had the lowest gain on 1/13/92. 9.5 Corbicula Burvival and Growth in Artificial Streams and River Bediments Corbicula mortality in the artificial streams was nearly nonexistent as only 3.3% died in the control and 100% effluent streams (Table 25 and F.i g . 6). Crowth was significantly different between control to 100% effluent, but it was not dose-dependent. That is, instead of growth declining with increasing effluent concentration, it was the reverse. Crowth of clams in the 100% effluent streams was twice as high as in the controls. In the river, clam mortality was nonexistent at all four stations but growth was significantly lower at all downstream streams compar e d to the 46
A T:ible 21 Sur.sval cnd growth of fathead minnew (C,metihales protnelas) larvae e= posed to Deaser Valley Power Station einuent for seven days from December 10-11. 1991. Larvae were exposed 10 efnuent containing CT-1 DT 1 for i day and to nushing of the mollusticide in the effluent for days 2 3 and 6 thereafter Sample size was IOur reDllCates of ten fish each Treatments significantly different from the contf oi are Indicated by an asterisk (*) at i w0 05 tevel Cone (%) t iort ality (* a i Growth (mg) SD 0 0 Control 00 0 902 0 101 50 00 0 817 0 074 10 0 00 0 713' 0 045 70 0 00 0 755' 0 043 40 0 00 0 764 0 099 100 0 00 0 703* 0110 O 47
I 1 Table 22_ Mortahty and growth of the midge (Chitonomus tiparius) after an instral exposure to artificial
'siteam sediments from the in-pfrnt dosmg operations. Sediment were collected from the streams at the field laboratory on January 13,1992,34 days after end of the in plant dosing protocol Mortahty Growth Stream Mean Duncan s n Mean Dry Wetght Duncan's Percent Multiple (mg iSE) Multiple Range Rango Control 6.7 A 3 1 425 (3 333) A 5% 67 A 3 1 390 (6 667) A f 1 , ' 50% ,
33 A 3 1 316 (3 333) A i 100 % 16'7 A 3 1 483 (12 02) A l i 4 F G b 48
l l Table 23. Moriality and growth of the midge (Chironomus tipatius) after a 10 day exposure to Ohio River Sediments in the laboratory at Virginia Tech Sediments taken from baskets in the river were freshly fallen matetlal. Mortality Gr owth Station Duncan's Mean Dry Duncan's n (%) Multiple n Weight Multiple Range (mg
- SE) Range Midge fest #1 Pre Dose Sediments Collected Aug.21,1991 j l
in (Intake) 8 1 25 A 8 0 414 (0 012) A ) P5 7' 5 71- A B 8 0.*S2 (0 019) A 28 7' 1 43 A 7' O 383 (0.040) A P10 8 16 25 0 8 0 429 (0 029) A
.t Midge Test #2 Post Dose Sediments Collected Aug. 23,1991 ,
in (Intske) 8 3,75 A 8 3 579 (0 018) A P5 7' 14 29 A 8 0 278 (0 039) C 2B 8 7.50 A 8 0 322 (0 067) BC Pio 8 7.50 A- 8 0.418 (0 030) AB Midge Test #3 - Post Dose Sediments Collected: Sep 26,1991 In (Intake) - 8 6.25 A 8 0 712 (0 026) A
. PS 8 8.75 A 8 0522(00?9) B ,
2B 8 13 75 A 8 0 571 (0 022 P P10 8 78.75 B 6' 0 496 (0 030) C Midge Test #4 Post Dose Sediments Collected. IJov. 5,1991
- in (Intake) 8 '5 00 A 8 0 872 (0 041) A PS-- 8 11.25 AB 8 0 889 (0 035) A !
30 8 28.75 8 8 0 833 (0 053) A P10 7'- 25.72 A B' 8 0 827 (0 028) A Midge Test #5. Post Dose Sediments Collected: Nov. 25,- 1991 4 in (intske) 8 20 00 A 8 0 547 (0.072) A P5 8 23.75 A 8 0 505 (0.134)
. AB 2B 8 33.75 A 8 0 454 (0.117) AB LP10. 8 63.75 B 7' 0 386 (0 198) B
' Based only on 7 replicates due to predation or other error in the test chamber, 8 Means with the_ same letter are not significan1ty different.
-
- Smaller sample size due to total completo mortality in other replicates.
49
Tnbie 24 Mortality and growth of the midge sironomus rrparsus) after a 90 day exposure to Ohio River Sediments in the laboratory at Virginia Tech $ccaments taken from baskets m the river were freshly fallen material. Mortality Growth Station - Duncans Mean Dry Duncan's n (" ) Multiple n Weight Multiple Range (mg
- SE) Range Midge Test #1. Pre Dose Sediments Collected Dec 9.1991 in (Intake) 8 6 25 A 8 1 382 (0 177) B P5 6 5 00 A 8 1 575 (0 192) A ,
28 8 0 00 A 8 1 620 (0 132) A P10 8 6 25- A 8 1 466 (0 218) AB Midge Test #2. Post Dose Sediments Collecied Dec.11.1991 In (Intake) 8 3 75 A 6 1445 (0 tii) A P5 4 7 50 A 8 1 572 (0.104) A 2B 8- 12,5 A 8 1.519 (0.114) A P10 8 15.0 A 8 1.451 (0.139) A Midge Test #3 Post Dose Sediments Collected. Jan. 13,1992 , in (Intake) ' 8 2.50 A 8 1 222 (0.035) B P5 8 3,75 A 8 1.330 (0.035) AB 2B 7 5.70 A 7 1 427 (0 084) A P10 8 15 0 A- 8 1 317 (0 058) AB
' Means with the same letter are not significantly different 50
, _ . _ _ - _ _ . . _ _ - . _ _ . - _ - _ . . - . . _ _ - _ . . ~ . _ _ . . . - . . _ . _ . - . - . - _
.S, Table 25 Means (SE1 of Cortncula shell tengths measured initially and 35 days after exposure to river control 5 50 ard 100' efflunnt m each of three replicate streams and in the f ever at four samphng stations Corcentration n Mean Growth Duncan s Mulbple (mm i SE) Range Artificial Streams 0% Control 29 0 632 (0 0281 A 5*. 30 0 685 (0 0195) A 50*', 30 0 948 (0 025) B 100 % 29 1320(0032) C in the Ohio River Station in 30 0 340 (0 026) A P5 30 0 184 (0 021) C 2B 30 0 219 (0 021) BC P 10 30 0,276 (0 039) B 51
Corbicula Growth in Laboratory Artificial Streams and River Sediments SHELL LENGTH INCREASE (mm)
/ -. ..
l
/
3,4 / . - _ . - . . . . -. .. - 1.2 - M
.Aj J - - - - - - - - - -- - - - '
j_ . 0.8 - ._L, - - - - - - -- - -
- 0. 6 - C ~- -
y 0.4 -
^
j
- 0. 2 - .- - - '
/ I
- I ,/
0
/ 7 7 7,/ /,
~
7L 7 >
~1' 7 0% 6% 50 % 100 % in P6 23 P10 .
ARTIFICI AL STREAW RIVER STATION PERCENT EFFLUENT REPLICATES L__j A i 18 Mc ' Mean and Standard Deviation Data Replicates A, B and C Combined ' SHELL LENGTH INCREASE (mr.1) 2 1.C --- -
~~
1- _ _
-~
0.5 -- --
--= - - - - - - - - - - -
-- ~~
j .- .. O i i i i i i i i i 0% 6% 60 % 100 % in ?5 28 P10 ARTIFICIAL STREAW PERCENT EFFLUENT RIVER DTATION I I MEAN Fig. 6. Graphics of Corbicula growth in laboratory artificial streams and river sediments iri the f all study. 52
pumphouse station (Table 25). Growth was lowest at the station (PS) c1ccest to the discharge. 9.6 Survival and/ or Growth of Selected Organisms in Laboratory Artificial Streams Mortality of all three organi sms in the artificial streams was either negligible to nonexistent (Table 26). One bluegill and a snail tal e d after 30 days, both being an a control stream. Bluegill sunfish growth followed the same pattern as observed for Corbicula growth. Fish growth increased with an increase in effluent concentration and was L' gni f i c ant ly higher in 100'. effluent streams (Table 27). Selected water chemistry measurements taken at various times from 12/9/91 to 1/14/92 in the artificial st r e ams are presented in Table 20. Temperature between the control and 100% effluent streams varied more than other parameters even though a water chiller was used to cool the effluent when it entered the main headbox. The temperature differential between these streams varied as low as 11.1 to 18,5 C to as much as 6.4 to 24.0 C. Conductivity, pH. alkalinity and hardness were elevated in the 100% effluent streams relative to the control streams. Dissolved oxygen consistently declined in concentration as effluent concentration increased. 9.7 Macroinvertebrate Monitoring in the Ouio River Table 29 presents tue benthic data according to major t axonomic groups (#/m ) fer the BVPS transects 1 2 2A. PS and 2B, prior to (12/9/91), two days after (12/12/91) and 35 days after (1/13/92) CT-1 dosing. At Station PS, oligochaetes and chironomids were greatest at all three campling dates. Mollusks were also most prevalent in the P5 left and P5 right stations during all three saanpling ef forts. These three groups of organisms were generally highest in the 1/13/92 sample. No unusual trends were evident between the three sampling dates for the broad taxonomic groups (Fig. 7). Nunber of taxa. Shannon-Veiner Index, eveness and richness are presented in Table 38 for each of the pre- and post-dosing sampire. At the bottom of the table, statistical indices ar e presented for each station on each sampling date based on the max t:num of the three replicate samples. In general, no single stetion stond out as being too high or too low in experimental variables r egar ding number of taxL prtMent. Uhannon-Veiner Index. eveness or richness (Figs. B-9). In general. Station P5 appeared to have slightly higher data than the other stations in the 12/9/91 samples. Diversity (Shannon-Weiner Index) tended to increate between the 12/7/91 to 1/13/92 samples taken from Station PS wnile trends between sampling dates for the other stations had no unusual trend. The lowest inde: values (<1.5) were found in Stations 1 A, 10, 2AA. 2AC and 2EM on either of the sampling dater but not with any chronological trend. The maximum divt. sity values ( >5.0) occurred in Station P5 for all three sampling dates and in Station 2B on 12/12/91. 9.8 Efficacy of Mollusc 1 cide - Corbicula Control in the Plant The ocatrol or eradication of Corbicula in the boxes housed within the ecoling tower be. sin W a not as successful as in the summer dosing effort (Table 51 ) . CT 1 was measurable from 0730 hra (1.5 mg/L) to Ok90 hr the following 53
Table 26 Percent CVmulative moriahty for Ine Auntic clam (Cort'tcula), bluttgill sunfish (Leporn#s mdCf 0ChlTU3) af\d a Snal) (GOnfobists) in art,ficial $1 reams housed at DVPS Test organisms tr sponses were evaluated after December 10.1991 on days 1. 7 15, 30 and 35 followin0 CI l 01 1 dosing info the plant Carecula R SunhSh Go roo b a sis S t ation ]. Uo_rt_shty Blues,
% tort ahty % uortahty
_ ~
'hy1 Control A 0 0 0 Control B 0 0 0 Control C 9 0 0 Elftvene 5% A 0 0 0 -
Effluent 5% B 0 0 0 Etnuent 5% C 0 0 0 Efnuent 50", A 0 1 0 Effluent 50% B e 0 0 Effluent 50% C U C 0 Effluent 100% A 0 0 0 Effluent 100% B 0 0 0 Effluent 100% C 9 0 0 Day 7 Control A 0 0 0 Control B 0 0 0 Control C 0 0 0 Effluent 5% A 0 0 0 Effluent 5% B 0 0 0 Effluent 5% C 0 0 0 Effluent 50% A 0 0 0 Effluent 50% B 0 0 0 Efnuent 50% C 0 0 0 Effluent 100% A 0 0 0 Efnuent 100% B 0 0 0 Efnuent 100% C 0 0 0
-Day 15 Control A 0 0 0 Control B 0 0 0 Control C 0 0 0 Ernuent 5% A 0 0 0 Ernuent 5% B 0 0 0 Etnuent 5% C 0 0 0 Etnuent 50% A 0 0 0 Efnuent 50% B 0 0 0 Etnuer t 50% C 0 0 0 Einvent 100% A 10 0 0 Efnuent 100% 0 0 0 0 Einuent 100% C 0 0 0 Day 30 Control A 0 0 0 Control B 0 0 0 Conteof C 0 10 10 Etnuent 5% A 0 0 0 Ernuent 5% B 0 0 0 Etnuent 5% C 0 0 0 Etnuent 50% A 0 0
- 0 Efnvent 50% B 0 0 0
. Etnuent 50% C 0 0 0 Efnuent 100% A 10 0 0 Einvent 100% B 0 0 0 Efnuent 100% C 0 0 0 Day 35 Control A 0 0 0 Control B 0 0 0 Control C 0 10 to Efttuent 5% A 0 0 0 Efnuent 5% B 0 0 0 Effluent 5% C 0 0 0 Effluent 50% A 0 0 0 tfnuent 50% B 0 0 0 Efnuent 50% C 0 0 0 Efnuent 100% A 10 0 0 , Effluent 100% B 0 0 0 Effluent 100% C 0 0 0 54 4 w- __ ____- __ _ . _ _ . _.___________.______m__ _ __ __
I Table 27 Moriahty and growth of tituegill sonhsh (Lepomis tracrechirust after an init'al esposure to e' fluent from the en plant cosing eperatione, Fish Aet e measured for inr f ease in growth by fork length and dry weight Stream Lenath Weight Contentration Mean Gain Duncan s Mean Dry Duncan s n (mm i SE) M u!tiple n weight Multiple Range (mgiSE) Range 0 0 Control 29 30 '44 (0 425) A 29 0 077 (0 004) A 5% 30 31 272 (0 309) 30 0 078 (0 003) A 50 % 30 30 775 (0 301) A 33 0 077 (0 003) A 100 % 29 31 533 (0 408) A 29 0 091 (0 004) B 55
Tatile 28 Water quality analy sis from the a'tificial stry.am (0 5. 50 100', offluenti system located within the DuQuesne Light CCmpan) $ envdOnmental Ial'Of 3 tory along with mea $ufements from the plume effluent Samples were taken before and after dosm9 with mollusticide e Date Sample temp Diss o' pH Cond Alkal Hardness and Hour (C) (mg / L) (umhosicm) (mg'L) tma'Lt 12/9/91 0'b Ern 11 1 - 6 56 325 - - at 5'sEm 10 6 - 6 78 335 - -- 1800 50'b Em. 12 3 - 7 21 461 - - 100% Eff1 15 4 - 7 63 592 - - Plume Em 18 5 - 7 98 659 - - 12/10/91 0% Em Bi 11 8 7 08 316 28 140 at 5?'. Em B' ii 8 7 12 328 30 120 0415 50% Em 12 5 10 4 7 48 483 42 180 100% Em 16 1 94 7 87 608 - Plume Em 18 8 94 8 00 SB8 51 220 12/10/91 0% Em. 79 12 0 6 97 353 30 100 at 5'/. Em 77 12 3 7 03 357 30 100 2030 50% Em 12 5 10 2 7 31 478 di' 160 100% Effl 16 5 96 7 44 576 - - Plume Em. 18 5 93 7.79 575 48 180 12/11/91 0% Em. 77 11 8 7 07 369 17 160 at 5'/. Em. 75 11 4 7 04 374 30 120 060G 50% Em 12.6 10.1 7 49 513 42 180 100% Em 16 1 92 7 73 606 - - Plume Em. 19 5 85 7.89 603 52 200 12/ C/91 0% Em 10 8 11 3 6 68 293 . 27 100 at 5% Em 10 6 11 3 6 73 291 23 100 0713 50% Em 17 8 91 7 31 413 37 180 100% Em. 23 2 7.9 7 60 582 - - 5 Plume Em 26.1 7.5 7 75 583 46 200 12/19/91 0% Em 65 12 3 7 09 250 15 100 at 5% Ein 6.5 12 1 7 10 297 29 120 0725 50% Effl 11.5 10 3 7 64 506 43 140 100% Em 14 8 94 7 88 634 - - Plume Em 16 7 93 7 9 B' ' 531 43 160 12/25/91 0% Em 58 13 0 6 86 337 22 100 at 5% Em 59 12.7 7 04 342 27 120 0630 50% Em 11.0 10.8 7 58. 570 46 180 100% Em 15.3 96 7 91 733 -- - Flume Em. 16.5 96 8 00 731 62 260 1/9/92 0% Em 64 12 9 6 94 317 29 120 at 5% Em 65 12 4 6 99 321 29 100 0600 50% Em 13 2 10.4 7 52 371 46 200 100% Em 19 4 8C 8 01 720 - - Plume Em 29 0 86 8.15 738 62 240 1/14/92 0% Em 10 5 12 C 6 84 334 30 120 at 5% Em 10 6 11 7 6 92 337 30 100 2700 50% Em 14 6 10 9 7 32 540 45 180 100% Em 18.5 86 7 68 725 - - Plume Em 2:i 5 75 8 07 754 59 280 56
l Tatste 29 Densities (numtier'quare meteri pe: major taxonomic group for tienthic sarnples collertr d at BVPS transects during the aquatic monitoring program tust priot (12:9'91) to dosing the plant with CT 1 two days latet (12'12/91). and 14 days (1'13/92) thereafter Date T aionomic of BVPS Transects Group Collection 1A IB 1C 2A.A 2A.B 2A C FS L FS M F5-R 2B-L 2B44 2B R Obgochaela 12'9'91 512 907 1537 1261 23B5 2444 79 1812 4789 B48 217 2543 12'12'91 394 355 234G 275 394 119 1989 769 3529 2028 0 2976 1/13'92 316 828 532 118 1005 375 1104 1970 6523 1616 59 5518 Chironomidae 12'9/91 59 40 59 1301 M99 1734 84% 592 11741 592 139 14538 12/12/91 20 59 413 20 118 20 1617 807 4906 1833 20 1931 1!13/92 20 39 20 39 257 40 3133 183217257 4217 79 10165 Mollusca 12/9'91 158 138 118 729 532 2%C 1433 59 1320 414 20 276 12/12/91 158 157 374 79 473 256 1083 118 1537 768 o 788 1/13'92 118- 315 197 394 256 394 1103 335 1241 453 0 276 Others 12'9!91 0 20 0 59 20 99 513 20 99 118 197 39 12/12/91 0 0 39 0 0 0 256 39 - 0 59 0 40 1/13'92 0 0 0 0 59 40 158 40 ' 79 119 158 138 57
T4ble 30 Diversity values for benthic mattoinvertebrate samples Collected from the Oh:o Rhet riurma the BVPS fate anr1 effects December 1991 nosing e.tudy Station Numner Parameter 1A 1D 1C Ib9 12 12 M 12 9 12 12 1-13 WG 12 12 1-13 No of Taxa 4 6 6 8 7 7 5 18 5 Shannon Weiner 1 40 2 08 2 11 1 81 2 31 1 98 1 30 2 82 1 77 index Evenness 0 70 0 81 0 82 0 60 0 82 0 71 0 59 0 68 0 76 Rtchness 0 46 0 79 0 82 1 no 0 94 0 85 0 54 2 02 0 60 Station Number 2AA 2AB 2AC 12-9 12 12 1-13 12 9 12 12 1 13 12-9 _12 12 1 i3 No of Taxa 14 7 4 13 7 11 21 4 7 Shannon Weiner 2 62 2 55 1 29 2 24 1 99 2 37 2.62 1 34 1 91 Index Evenness 0 69 0 91 0 64 0 61 0 71 0 69 0 60 0 67 0 68 Richness 1 60 1 01 0 48 1 39 0 87 1.56 2 38 0 50 0 89
~'
- Station Number PSR P5M P5L 12 9 12 12 1-13 i2-4 12 i2 1 13 12-9 12 12 1 13 No. of Taxa 26 23 21 it 14 17 14 23 26 Shannon-Weiner 2 59 2 83 2 26 2 05 2 84 3 20 2.50 3 14 3 31 Index Evenness 0 55 0 63 0 51 0 56 0.75 0 78 0 66 0 69 0 70 Ric iness 2.55 2 39 1.97 1.54 1.74 1 92 1 63 2.59 2 90 Station Number 2BR 2BM 2BL 12-9 12-12 1-13 12 9 12-12 1-17 W 11,2 1 IT No of Taxa 21 25 31 9 1 7 15 19 22 Shannon Weiner 1 67 3 60 2 51 2 50 0 b0 2 34 2 93 3 00 2 45 Index Evenness 0 38 0.78 0 51 0 79 0 00 0 83 0 75 0.71 0 55 Richness 2.05 2.77 3.10 1 26 0 00 1 05 1 85 2 13 2 40 Values calculated for the maximum of three replicate samples from each station Station Number i 2A P5 2B 12-9 1212113 12 W 1212113 12 9 12121-13 129 1212113 No, of '.'axa 8 19 9 23 10 12 35 35 35 27 30 37 Shannon Weiner 2.19 2.84 2 03 2.58 2.24 2.32 3.10 343 303 203 3.53 2.67 Index Evenness 073 067 064 057 068 065 060 067 0.59 0.43 072 0.51 Richness 099 247 120 2.62 1.41 1 59 380 3.94 3 63 296 356 403 58 4<
BVPS FATE AND EFFECTS AUTUMN 1991 BENTHIC SAMPLES - CHIRONOMIDAE DATA NUMBER OF CHIRONOMID 8/80V ARE METER j
/
20,000 I 16,000 - tw
,=..
10,000 - 6,000 - ja/a/w/ /e- ' / 1 fc==/wjts/ p:r/ 7 m y/ygv, , - ,- - a , , , , , 7, ., ,/ 1A 18 ifi 2A A 2 A B 2 AC PSL P6M P6R 2BL 2BM 2BR BVPS TRANSECTS SAMPLlHO DATE I I Dec. 9,1991 C D ec.12,1991 M Jan.13,1992 BVPS FATE AND EFFECTS AUTUMN 1991 STUDY BENTHIC SAMPLES - OLIGOCHAETA DATA NUMBLR OF OLIOOCHAETES/ SQUARE METER 7,000 - . _ . 6,000- _ _ _ . _ , ,_ ,_ ,,_ __ _. 6,000 - c 4,000 - 3,000- ,_ c _ c= , w , _,,, ._ _ _, __, _ 2,000 - M: W
= ~
1,000 - $2 ~ "2 2 ,. 7 g }/ s7/ j_ _ _ c= . 0 i i
} /, / ,-.
i
. /
i i
/ /a.?/-Q, i , ,
./i / _ i i i
1A 18 1C 2AA 2 AB 2 AC P6L P6M P6R 2BL 2dM 2BR BVPS TRANSECTS SAMPLING DATE I I Dec. 9,1991 1 I De c.12,1991 M Jan.13,1992 F;g. 7. The density of chironomids end oligochaete s for the f all sampling effort in the 0hio River. 59
BVPS " ATE AND EFFECTS AUTUMN 1991 STUDY TOTAL NUMBER OF TAXA PER BENTHIC SAMPLE NUWBER OF TAXA 1 36 / '
- ~ '
30 - -- - -- -- - -
" -- - c' , ' '
~
25
} -"
~
~~' ~
20 - - - - - * - -- -------- - - - - - - - -
~
- 16 - - - - - - --
w --- ~ m:~ '- - - 10 - mWL -r --' e . 1
~- -
S
/ 7, k _3 _ $._ Ij _O y 0 NL_.
1A 19 1C 2 A A 2 A8 2 AC P6L P6M P6R 2RL 28M 2BR g BVPS TRANSECTS SAMPLING DATE L J Dec. 9,1991 C Dec.12,1991 M Jan.1s,1992 BVPS FATE AND EFFECTS AUTUMN 1991 STUDY TOTAL NUMBER OF ORGAN 18MB/SOUARE METER HUMBER OF ORGANISMB/SOUARE METER
*/
_j . - . _ . - . . . - - 26,000 - 20,000- e, ,
. .n _
16,000 - 10,000- . 6000- 'W
- o. / r- ,
h _. - ,A ._- , W 5 i i i . i i , i i i 1A 19 1C 2AA 2A3 2AC P6L P6M P6R 2BL 2BM 28R BVPS TRANSECTS SAMPLING DATE R Dec. 9,1991 L_J Dec.12,1991 E Jon.13,1992 Fig.8. The number of taxa and density of invertebrates for the fall sampling effort in the Ohio River. 60
BVPS FATE AND EFFECTS AUTUMN 1991 STUDY SHANNON-WEINER IN0 ICES - BENTHIC SAMPLES
$H ANNON. WEINER INDEX
. / 4' =' 4 S{ , 3.5 - ,, {
~
S g 3-g ,. .. . j [., m
=- - ;, _ -
2- = , j . . _ . . . _ .-
,7 7-- .'?
.k.k,j'7L,9.k,7 0
/ _,9_
i i f i i i i i i i u. i d J_f i 1A 18 10 2 A A 2 AB 2e.C P6L P6M P6R 2BL 2BM 2BR BVPS TRANSECTS SAMPLING DATE i I Dec. 9,1991 1 I D e c.12,1991 E Jan.13,1992 BVPS FATE AND EFFECTS AUTUMN 1991 STUDY RICHNESS VALUE8 - BENTHIC SAYoLES MICHNESS WLUE 3.5 '
/ .,
~'
-pcz .-. . - .
.g ._ . e _
c', :1 ___. _ 1.5 - c' y
, c , . _ _ . _ _ . . _-
0.5 - T T T ^ s _,/ , , sf _,b __
=,
W n 7 ps, >/, / . . 7 ,7 (_r , /(7 ,7-
/, /-,7.>7,-
7 1A fB 10 2AA 2AB 2AC P6L P6M PSR 2BL 2BM 2BR BVPS TRANSECTS BAMPLING DATE I 10ec. 9,1991 L J oec.12,1991 E Jan.13,1992 Fig. 9. Shannon-Weiner Index and richness of invertebrates for the fall sampling effort in the Ohio Ri ver. 61
Table 31 Efficacy of molluscirede Corbicula conttni in the Cochng Tower sti basin after the fall 1991 dositig efloti Clims in tus'tets were espesed to CT 1 for O( A). 6(BL 8(C) 10iD) 12tE) 14t r ) 1G(G) and >irdh) his Clam moitality is usted Uy adults (1215 mm) and. in patentheses
, IUveniles (7 9 mm)
CT.1 Dosing Clam Mortality (% Hout Cont (ppm)' Day' A B C D E F G H 0730 <0 2' 1 0 0 0 0 0 0 0 0 0810 c0 2' (0) (0) (0) (0) (0) (0) (0) (0) 0730 1$ 2 0 0 0 0 0 0 J 3 0830 20 (0) (0) (3) (3) (0) (3) (0) (0) 0930 30 3 0 0 0 0 0 0 0 3 1030 45 (0) (0) (3) (3) (0) (3) (0) (0) 1130 49 4 0 0 0 0 0 0 0 3 1230 61 (0) (0) (3) (3) (0) (3) (0) (0) 1330 61 5 0 0 0 0 0 0 3 7 1430 7.1 (0) (0) (3) (3) (13) (20) (30) (30) 1530 77 6 0 0 0 0 0 0 3 20 1630 83 (0) (0) (3) (7) (30) (23) (40) (70) 1730 81 9 C 0 0 0 0 0 3 43 1830 10.5 (Os (0) (3) (10) (33), (37) (40) (87) 1930 10 3 12 0 0 0 0 0 0 3 43 2030 12 3 , (0) (0) (3) (10) (33) (37) (43) (87) 2130 11.3 15 0 0 0 0 0 0 3 43 2230 10 5 (0) (0) (3) (10) (33) (37) (43) (87) 2330 72 20 0 0 0 0 0 0 3 43 0030 52 (0) (0) (3) (10) (33) (37) (43) (87) 0130 40 25 10 37 27 27 37 27 27 43 0290 13 (7) (3) (10) (13) {33) (40) (57) (87) , 0290 >0 96 0330 0.59 0330 0 43
' Concentration is CT 1 measured in the CoolinD Tower prior to clay detoxification.
8 Day represents time after plant do;ing in which clam mortality was observed. 8 Measured concentration of CT.1 off scale and officially measured a second time. 62
morning but the optim.=1 dosing levels (ie.. 6-12 mg/L) occurred between 1230 and 2339 bra. Adult clam mortality reached 43% in the longest exposure whils 87". of the juveniles died. Although clam mortality was monitored up to 25 cas after crposure, most clams died af ter the first nine days. Clams left in the tower for 16 hrs or less had minimal mortality, as low as 271, for adults. No detectable residuals of CT-1 were measured in the main effluent during the fall dosing (tam e 32). A total of 5.292 and 4.549 lbs of DT-1CT-1 respectively, were used. The pounds /br of DT-1 and CT-1 delivered into the plant are found in Table 33. The overall ratio of DT-1 :CT-1 was 1.2/1 in the fall dosing which was somLwhat lower (1.4/1) than that used in t' summer. The total amount of DT-1 used in the fall was 1.195 lbs less than in the summer. 9.9 Monitoring of To _al Suspended Solida during In-Plant Dosing The TSS levels measured in the main effluent ranged from 28.77 ppm at 0930 hr to 68.49 ppm at 2130 hr (Table 34). Prior to dosing at 953s and e638 hrs. offluent TSS was 26.86-37.26 ppa. Turbidity in the river, as measured from the intake TSS. ranged from 14.15 to 24.49 on the day of doe s ng. The river was ~3-fcid more turbid on 12/10/91 than in the summer dosing. Some of the TSS neasurements . during the fall varied from 4.95 ppm in September to 2.65-7.49 ppm in November. 10.8 DISCUSSION 10.1 Ceriodaphnis dubia Survival and Reproduction In the summer dosing study where two reproductive impairment tests were carried out. Ceriodaphnia survived and reproduced well in Ohio River water since it was not turbid. In tl.e initial, dosing study of low river turbidity, neonate reproduction was greater in control water .(39.1) and lowest at 188% effluent (4.1) (Table 1). One week later, this test was repeated with the sare effluent and neonate production in 189% effluent was similar to the controls (Table 2). In the fall dosing, the consequences of effluent-caused impairment improved from 1e% effluent concentration to t.o effect nt 188% thirty-five days later. In fact, reproductive success increased with increasing effluent concentration (Table 29). -Turbidity of the effluent was similar in both summer and fall dosings while river water was *3-fold higher in TSS in December. Test requirements concerning diet, water hardness , pH fluctuations. and population source for Ceriodaphnia have been addressed recently in the peer-reviewed literature (Belanger et al.1989. Belanger and Cherry. 1998). but turbidity extremes with river runoff toxicity complicated the Ceriodaphnia test results at BVPS in 1998. This situation becomes more compler when a molluscicide with clay'is added into it. In 1991.'it appears that too little turbidity in the river water _ may have influenced the reproductive impairment of one test organism in the effluent while dosing of the plant occurred. A certain amount of natural turbidity may help in binding all the reactives in the molluscicide. From the chronic response of Ceriedaphnia, which had 188% sury;tval and high reproduction in 20% effluent during clear water conditions, it is seen that the effluent with molluscicide and clay did not cauce impairment at the instream w ste concentration (IWC). That is due to the dilution ratio for the volume of 63
Table 32. Concentrations of CT.1 in the mam efnuent during in-plant dosing in December 1991. Date M ain Hour Einuent tppm) 12/10 0500 <2 12/10 0530 <2 12/10 0630 <.2
~
12/10 0730 <2 12/10 0830 <.2 12/10 0930 <2 12/10 1030 < .2 12/10 1130 <2 12/10 1230 < .2 12/10 1330 <.2 12/10 1430 <.2 12/10 1530 <.2 12/10 1630 <.2 12/10 1730 <.2 12/10 1830 <.2 _ 12/10 1930 < .2
.12/10 2030 <.2 12/10 2130 <.2 12/10 2230 <.2 12/11 0030 <2 12/11 0130 <.2 12/11 0210 < .2 12/11 0330 <.2 64 l
y .- _ _ >.-m. . - . _ . . _ . _ . - - . _ . _.~... _._. -- _ - . -_.
=-
y
.:s
~Tabte 331CT.1 (molluscicide; and DT-1 (beritonite clay) feed rates during in plant dos.ing on December -
10-11. 1991? t Date : Hour . CT-1.
- Slurry- Slurry DTE DT-1 R atio* - 1 (ids /h.) (Ibs/hr) .- (ppm) (Ibs/hr) (ppm) OT-1/CT 1 12/10/91 0600- - 8.7 '34 8 22 6 34 - 6
. 12/10/91 0607 153.9 8.7 : 34 8 22.0 3.4 02/1' 12/10/91 - 0636 '305.9 8.7 34 8 22.6 34 0.1/1 12/10/91: 0745J 365 9-- B.7 34 8 22.6' 34 01/1
, 12/10/91- 0800 365 9. -B7 34 8 180.0 25.7 05/1 12/10/91 -0525- 352.3 8.7 34.8 180 0 26.7 0.5/1
- _ .12/10/91.- : 0830 - 352.3 10.4 41 6 180 0 26.7- 05/1
- 12/10/911 0856- 348.8 - 10 4 41 6 - 180 0 26 7 0.5/1 ,
j -:-12/10/91 - 0915- 301 0 10.4 41.6 258 0 38 3 O 911 12/10/91- 0945- 301.0'- 8.7 34 8 258 0 38 3 09/1 h 112/.10/91 -
-:12/10/91
- 0956 1345.'
297,5 237.5 8.7 8.7
.34 8 41.6 258 0 ^
3240 38.3 48 0 0 9/1 1.1/1
'12/10/91- 18002 297,5 10 4- 0 324 0 48 0 1.1/1 92/10/91 1920' W5 . 0 324 0 48 0 1.1/1
- 12/10/91- 2050 1 3920. 58.1 2.4/1 12/10/91 ' 2115 .0_' 392.0 58.1 ,
, 12/10/91 2250 - 2580 38 3 12/10/91 2450 -
180.0 26.7 12/11/91 - 0100- 68 0 10.1 l12/11/91 0200 .45.0 6.7 , -- 12/11/91L . 0400 22.6 3.4 712/11/91 ; 0500: 0- 0' i
- DT-1 and CT 1 used was 5,292 and 4,549 lbs. respectively.for an overall ratio of 1.2/1."
' " To minimite solids addition into the receiving strearn, DT 1 feed rate was based on system demand-
- of CT-1 levels rather than on CT-1 feed rate, so the ratios listed did not approach the theoretical i: optimum of 1.5/1 or 1,4/1 in the Summer Study.
t _ '_. 65 e o- + y ,. , --r,. -r. , .y .,a.,,- -- 4
m t
' s Table 34 Total suspen< led solids (TSS) levels within the Ohio River before. during and after dosing of CT 1 DT 1 within the plant at the intake and main elDuent station from September 29 through December 11,1991, Period of in Plant Oosmg and TSS (ppm)
Hour intake TSS Main Effluent-TSS December 10.1991 0530. 16.30 37.26 0630 14.15 26 86 0930- 22.78 28.77 1230 15,16 - 33.26 1530. 18.76 27.79
.1830 - 16.88 -i 58.10 .
2130 21.28 68 40 2330 24.40 59.81 December 11,1991 f
.0030- 12 82- 22.33 1000- 23.79 44.56 December 12,1991 1300 30 45 72.92 December 13,1991 0720 22.18 23.96 Predosina -
11300- -4 05 Sept 29 - 31.38
-1300 4.95. Oct 18 .- 15.88 l E1300- 3.16: .'Oct 25 10.1 1300 ' 7.49. Novi 15.5
,1300- . 2.65 - Nov 8 14.54 -
1300 3.31 Nov 15 - 9.18 1 300 3.12 .Nov 31 - 13.56 1300: 31.04 Dec 7 51.18 66 i. r - -- .,
l
- effluent $ per river volume du-ing low flow conditions which is 5% or less. In
;both: the summer and fall dosings, no negative effects on survival and reproduction occurred at the IWC.
n 10.2 Fathead Minnow Survival and Grovth The fathead ninnow survival / growth impairment test in August 1991 could be
. labelled by some as the " textbook" test, that is, nothing unusual happened anywher e. - No fish died at the control or any erP uent concent. ation - and weight l 4ain increased as the percent effluent concentration increased. Veight gain was l
in direct proportion to the effluent strength. In the December 1991 dosing, fathead minnow mortality was 8 at all test concentrations. The slight differences in weight gain at some of the higher effluent concentrations was due to the " tightness" of the test in that variability was very slight. The fathead minnow test allows for the evaluation of environmental stress
-by using an organism that could forage upon daphnids. It also measures biomass
.or. weight gain which is a different physiological parameter than reproduction.
. Although less sensitive than - Ceriedaphnia in this effluent testing, there are ccses where.it is more sensitive to specific toxicants with nitrogenous elements and high oxygen demand. - The testing of both test species allows for. a trophic level evaluation (ie..-two different ecological levels of food consumption) of potential toxic effects - into the Ohio River when in-plant desing occurs. Based on the chronic responses of the fathead minnow, which had 100% survival and high '
growth in 188% effluent ' during cleyrer water conditions. it is apparent that the l effluent with- molluscicide and clay causes no impairment to this test species at and near the IWC. 18.5 Chironomus survival and Crowth The Chironomus_ test provides an evaluation of chemical fate and effects of organisms residing in river sediment. After the plant, is dosed with molluscicide and clay. these by-products in the effluent eventually settle out in the river codiment. In 1998 the baseline and spring study tests indicated that a bcckground t contamination of the river sediment unrelated to this study occurred balow the plant. To address this situation and the consequence of actives in the effluent settling out into the river sediment. a collection device or tray was utilized which was- originally developed by Shema et al. (1989) to document the invasion of Corbicula larvas settling into the cooling tower sediment of - BYPS. Unfortunately, the amount of eediment collecting in these trays was minimal due to the unusually low precipitation conditions that occurred ' there in the summer of 1991. Hence, dilution of river sediment by normal seasonal precipitation did not-happen in the sampling trays. Although the predosing tests indicated no growth impairnent of Chironomus at any station in the river, the _ innsediate and 40-day post-dosed sediment tests
-chowed that stations in the' river below the main effluent discharge contained .-
sediments that impaired midge growth. Additional midge testa vere carried out to ovaluate this condition prior to and during the fall dosing procedure c.t .the plant. The l nediment situation cleared up prior to . the December 10, 1991 dosing and ' remained that ' way until after initial dosing and ' 35 days later (Tablet 23-g 24). Data from sediment collected- in the artificial streams showed no I. eignificant survival, or weight impairment following 35 days after dosing the plant, hence supporting the findings in the river study. 67 l-l-
10.4 Corbicula Crowth Rates Corbicula growth rate results in the river sediment were similar to those of the Chironomus growth test, that is, clams in the first two stations below the effluent were significantly impaired in growth. The intake and Pt s stations were not growth impaired for clame. New clams were added to the trays in the river to further assess the impairment problem observed in August-September 1991. Growth was significantly lower in the river stations below the plant and by the time the dosing occurred in December 1991, the cold river temperatures inhibited any growth recovery potential. In the laboratory where effluent temperature was high enough above ambient to stimulate clam growth, it occurred at significantly higher levels as the effluent increased from 5 to Se to lee % effluent (Table 25). Therefore, the laboratory artificial stream system provided information that showed thermal enrichment to influence the potential effects of CT-1:DT-1 and found them to be negligible. The increased effluent temperature fostered a thermally enriched environment that override any potentially negative influences of CT-1:DT-1. The artificial stream studies assessing Corbicula growth rates in the laboratory did not validate the results in the river (Fig. 2). Overall, clam growth in all artificial streams, including 188% effluent, were substantially-higher than tha'. recorded in the Ohio River stations. 18.5 Advantages of an On-Site. Experimental Stream Laboratory The strength of this research program, which attempts to discern the potential for harm to the receiving system from CT-1 DT-1 release, is derived from its diversity of tests. This diversity includes laboratory . toxicity-testing, on-site experimental stream testing and river biomonitoring. Any one of these-three alone is iheufficient, since each one has strengths and weaknesses of its own. It is important, however, to acknowledge that formal laboratory toxicity testing has its flaws. First, there is no environmental realism in a laboratory test beaker. This overly simplistic environment is extremely different from the real world receiving system. This artificial environment may enhance the sensitivity of test organisms. In addition, the laboratory tests wy indicate a much higher level of sensitivity than in the river where compounds may be subject to environmental sinks, transformations, hunic acid chelation, etc. Also, there is concern that single-species tests in the laboratory cannot predict multi-species, cosssunity and ecosystem responses accurately (Cairns. 1983). The
' laboratory test species that were used to develop the national criterion may not be representative- of the receiving system in question. A single, national criterion or number may be protective for one region of the country. less -protective fcr .another, and perhaps overprotective. for a specific receiving system. I The experimental stream system has several advantages over formal laboratory toxicity testing. These streams have environmental. reallem since river water and effluent ~ can be released into them simultaneously. Endemic organisms can be used for testing without the concern of laboratory-associated stress problems. .That is, the native food components are pumped directly into these streams so artificial food is not a concern. It the receiving cystem water quality is acceptable, alterations of river water characteristics by shipping and 68
r. l storing is avoided in these once-through systems. Test organisms can be tested over longer periods of time (ie., months rather than days). The evaluation of obiotic processes influeacing fate and effects of detoxified molluscicides is Oddressed in a real-wcrld, realistic manner. Replicability of specific diluent / effluent concentrations is available. Toxicity testing and longer-term impairment testing can be carried out addressing ecological and physiological requiremento. Organisms inhabiting a fast-flowing receiving system can be placed into a similar, f ast-flowing experimental stream without suf f ering physiological or metabolic stress. In addition multiple species testing can be carried out in the same stream system to relate to the concern of multiple species effects in the receiving system. Since there is an abundant number of pros and cons for both single species laboratory toxicity testing and for more advs.nced testing systems- (biosurveys ).
~
the best approach is the weighted one (use both). The National Research ' Council (1981) endorses thic position. They say. " Single species tests. if appropriately conducted, have a place in evaluating a number of phenomenon affecting an ecosystem. However, they would be of greatest value if used in combination with tests that can provide data on population interactions and ecosystem processes." Companies who wish to develop a data base for both should not be penalleed by being limited to one. There are more important issues here than the desire to use the simplicity of a single number generated from a simplified, laboratory toxicity test. In a position paper on derivation of site-specific water Quality Criteria by the US KPA in Denver. Co. Dec. 31 1981 it was stated that the site-specific guidelines recognize ,that " national criteria [as generated by formal laboratory toxicity testing] may not be applicable to species in specific bodies of water because of biological, chemical, and physical variables." (Keefe et al. 1981). They endorsed the results from two approaches: on site toxicity testing coupled with a site-specific stream survey, because national standards often do not reflect local conditions.
~
10.6 Invertebrate Survival in Artificial Streams The artificial stream system, as noted in section 10.5 provides an additional realm of environmental realism that formal laboratory survival-impairment tests (ie.. Ceriodachnia) do not. That is, test organisms taken from a fast moving, lotic environment are housed and tested for 48 days in an environmental similar to their natural location. Unaltered river water is used as the diluent on a once-through flow arrangement. Organisms feed on the natural food source that either colonizes or paases through the. stream system. Hence. the ecological integrity of large macroinverttbrates (enails, clams, insects) in the river receiving system is addr es sed with environmental realism and test replicability. In the summer study. neither Corbicula nor Goniobasis survivorship was significantly influenced in the 5 or 50% effluent treated streams (Table 8). Bluegill sunfish responses, however, were more difficult to evaluate. Bluegill survivorship was significantly lower in the 58 and tee % effluent streams but fish growth and weight were not impaired. Some difficulties lie in the fact that acclimation time v a not considered for bluegill, especially since fish mortality became significant later in the test (last 30-48 days). In the fall dosing study, bluegill were acclimated in Ohio River vater for 1 month prior to exposure, and then placed in the artificial streams at the B'd PS Plant. Since bluegill mortality was negligible after 30 days of acclimation, they were 69 l
an acceptable test species; for use in the Ohio River system. During and through 35-days after dosing, bluegill ' mortality was negligible (Table 26). Appar ently. the -preacclimation period of 38 days was an important improvement in this test. Bluegill- growth data supported the survivorchip data and showed that at 100'. effluent, growth was significantly enhanced over the controls. 18.7 ' Macroinvertebrate-Monitoring in the Ohio River
' No unusual trends were noted for macroinvertebrate distribution between ,
river -. stations above Lversus below the plant or between pre- and post-dosing of the plant in the ausener and fall. Macroinvertebrates were least abundant where
- little sediment '.was available in the main river channel. Where the sediment was of fine particulates, chironomids and oligochsstes (worms) predominated (Fig. 3).
The patchy distribution = of macroinvertebrates in the river during 1991 was similar.to that found in 1999 (Cherry et al . 1991 ) . This patchy distribution was similar to that reported in the historical data base by Shema of Aquatic Systems Corporation (Shema et al.-1989). Taxon richness generally increased during the
- three summer, samplings (Figs. 4-5).
Invertebrate abundance, richness and diversity before and after each plant dosing showed no negative fate and effects consequences upon benthic macroinvertebrates in the Ohio River. . 18.8 ' Foam Froduction in Effluent and CT-1 DT-1 Totals Foan in the effluent was not generated during the summer or fall 1991 s dosing of -the plant. .It can happen from the oxidation' of the mollusc 1 cide with
= - slime buildup in river ' water service anes, heat exchangers, and the cooling tower, especiallyf 'since Unit 2 Cooling Tower has not been dosed previously. The release of bentonite clay for, detoxification purposes may enhance this problem.
During dosing. the ratio of CT-1 DT-1 was maintained at 1.4/1.9'in the susumer to 1.2/1.8 in - the fall. No _ detectable levels of CT-1. were observed in the effluent except ' for three measurements taken- during the latter-part of the dosing in the smaller flow of the auxiliary effluent in Unit 2 during August 1991. CT-1 was not detected in the affluent of Unit ,1 1p December 1991.
. The. problem regarding foam production during the molluscicide application Lin'~the spring of 1998.was eliminated in the fall of '1990 and again in the summer and fall of 1991.- A~ systen of sprayer jets was attached over and around the final ' channel of the effluent L raceway and operated continuously. As effluent with CT-1 DT-1: passed through the - baffles of ths raceway, the water -jets broke.
- down the " developin6 foam. A double boom ~ was placed in the initial discharge channel of the river.to contain residual foam that passed through the sprayer jet Jsystem. The amount of CT-1 ' administered in the summer of 1991 (4.643 lbs) .was :
'less than that used in the fall dosing of 1999 (4.959 lbs). The amounts of DT-1
, and _ CT-1.were '5.292 and 4.549. respectively in the 1991 fall dosing. These were slightly less than the amounts applied in any previous dosing efforts. 10.9 . Clan Control during Summer and Fall Dosing The - molluscicide-clay dosing in the plant was considered to be highly effective l for ' Corbicula control = in the summer. Live boxes containing 38- clama each were suspended from Unit 2 Cooling Tower. Clam mortality was 188% (5 days t. later) when: CT-1 concentrations measured from <t.2 to 13.s ppa in 16 hrs of exposure 'in the cooling tower. In the fall dosing. molluscicide treatment was not - as optimal as in previous dosings since only 43% and 87% of the adults and 70
i juveniles died. The reduction in CT-1 used as well as the colder river t emper atur es during December 1991 versus November 1998 were considered to be responsible. Within the plant, however. CT-1 levels were presumed to be much
-higher and probably caused 188% kill although bioboxes to evalutte this premise
.were not used during the fall 1991 dosing.
11.8
SUMMARY
-- 1991 SUMMER AND FALL STUDIES This report contains the results of two distinct studies. summer and fall dosing studies of Units 2 and 1 respectively, in the plant. The sumetr and fall studies were carried out on August 21-22 and December 10-11 1991 when the plant was dosed with a molluscicide (Clam-trol (C". -1 ] ) . Survival /impkirment and fate and effects studies followed for 7-48 days thereafter. A three-tiered l eva/1 of testing was conducted which included formal laboratory testing, on-atte experimental stream evaluations and river monitoring of benthic macroinvertebrates.
11.1 Summer Dosing Study On August 21-22, 1991, the plant (Unit 2) was dosed with CT-1:DT-1 for "18 hrs in an effort to control Corbicula infestation within the plant. The formal laboratory toxicity-impairment terting occurred at Virginia Tech while artificial stream evaluations of the effluent occurred in the environmental laboratory at the plant. Benthic macroinvertebrate densities in the river were evaluated to corroborate the laboratory and in-river studies. Ceriodaphnia survived an acute effluent CT-1:DT-1 exposure of 5 to 48% but had 188% mortality at 188% effluent. Ceriodaphnia suffered no significant mortality or reproductive impairment at (28% effluent, while fathead minnow had no deleterious consequences through 188% effluent. Therefore, no impairment occurred at the IVC which was 5% effluent. When the same effluent was evaluated
~2 weeks later, no negative survival or reproductive impairment c'ould be found through 188% effluent concentrations.
The CT-1 :DT-1 dosing in the plant did inhibit Chironomus growth in the river sediment station downstream out not in the sediments of the laboratory artificial streams. Chironomid growth in the river sediments below the plant a.t P5 and 2B contir.ued to be impaired through the 48 days following molluscicide dosing. Subsequent testing of the river sediments was developed in the talk prior to dosing to determine the potential for recovery. Corbicula growth was impaired in the artificial streams at 58% offluent but not at 18 8". . In the river. Corbicula growth was impaired at Stations P5 and 2B 35 days after dosing. Bluegill sunfish growth in the artificial streams was not impaired after desing but survivorship was. Effects upon snail (Goniobasis sp.) and Corbicula survival were negligible throughout the artificial stream studies. Macroinvertebrate benthological data were similar before. just after and 48 days after in-plant dosing. Organism occurrence and dsnaity were patchy and a function of the type and amount of sediment available. No foam was generated in the effluent during the in-plant doning with CTm 1:DT-1 as a result of oxidation of slime (algal, fungal, bacterial) buildup M river water service lines. Clame held in bieberes in the Cooling Tower were successfully eradicated within 5 days followieg exposure to CT-1 and in general. 71 l l
both juvenile and adult clams were equally sensitive. 11.2 Fall Dosing Study On December 10-11, 1991, the plant (Unit 1) was dosed with CT-1:DT-1 for a period of 16 hre for Corbicula control af ter the fall spawning period had ended. As in the spring study. three tiers of testing (formal laboratory, on-site laboratory, macroinvertebrate monitoring in the river) were utilized. In tne 7-day survival-impairnent tests, Ceriodaphnia survival and reproduction were 'not affected at the IWC but had reproductive impairment at 10% effluent concentration and higher. Fathead minnow survival-impairment tests indicated survivorship occurred through 100% effluent while the NCEC was at 10% effluent. Prior to alant drding in the fall, sediment at Stations P5 and 2B vere evaluated for pc tenti si impairment of Chironemus growth. No impairment was ctserved in the 9/29/91 sample or in subsequent samples taken on 11/5/91 and 11/25/91. The CT-1 DT-1 dosing in the plant did not, inhibit Chironomus and Actatic clam growth in the river sediment or in laboratory experimental streams. In general, growth was greatest ~at the river station closest to the effluent discharge and in the 59 and 100% effluent-treated streams. Survivorship was
~100% for both sediment-dwelling organisms. Survivorship of snails (Coniobanis sp. ) in the artificial streams was 1ee% and nearly so (~955) for Corbicula. This trend continued after 35 days into January 1992 and indicated that potential .
thermal enrichment influenced the ecological integrity of.the sedimests in the , on-site laboratory and river receiving system. Patterns of macroinvertebrate benthological data were similar to those found in the summer study and earlier (spring and fall, 1999). Macrcinvertebrate benthological data had no unusual tret.de among each of the sampling periods before, just after and 34 days af ter in-p1Lant dosing. Where , sediment was limited in the middle of the discharge cht.nnel, organism abundance van patchy. Organism occurrence and density were a function of the type and amount of sediment available. As was the case during the cummer desi g of the plant, foam generation was not a problem during the fall. Clams held in bioboxes in the Cooling Tower vere not as successfully controlled as they were during the summer dosing. A1't e r 25 days of surveillance. 45 and 87% of the adults and juveniles, respectively, were eradicated. 72
i 1 1 12.0 LITERATURE CITED Belanger. S.E., . J . L. . Farris and D.S. Cherry. 1989. Effects of diet, water har dne s s , and population source on acute and chronic copper toxicity to l Ceriodaphnia_dubia.. Arch, of Env. Contam. and Tox., Vol 18 pp. 601 611. Belanger . S.E, ,- J.L. Farris. D.S. Cherry and J. Cairns, Jr. (In Press).
, Validation of Corbicula growth as a stress response to copper in artificial and natural streams. Can. Journ. of Fish, and Aquat. Sc i'.
Belanger. S.E. and D.S. Cherry. 1998. Effects of pH and heavy metals to Ceriodaphn13 pH acclimation, acute and chronic toxicity. J. Crustacean
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Cairns, J. Jr. 1983._ The case for simultaneous toxicity testing at different levels of biological orga.nization. ASTM Spec. Pub. 802 Philadelphia,
, Pennsylvania.
Cherry, D.S., J.L. Farris. J.R. Bidwell. A. Mikailoff, R.L. Shema and J.M. McIntire. 1991. 1993 Corbicula Control Program - Environmental Fate and Effects Studies - Baseline, Spring and Fall Dosing Studies. Duquesne Light Company.. Beaver Vr.11ey Power Station. Shippingport. PA. 116 pp.
.Giesy, J.P., R.L. Graney J.L. Newsted, C.J. Rosiv. A. Benda. R.O. Kreis Jr. and F.J. Horvath. :1988. Comparison of three sediment bioassay methods using Detroit River sediments. Env. Toxicol. Chem. 7(6):483-498.
Hollander. - M. sad D.A. Wolfe. 1973. Nonparametric Statistical riethods . John Wiley & Sons, New York, N.Y. Keefe. D.F... D.R. Nisano. D. Baldridge and G. Iley. Jr. 1983. Field investigations . and on-site toxicity testing: an assessment of habitat suitability-Arkansas River. Pueblo, Colorado. ASTM Spoc. Pub. #882 Philadelphia, Pennsylvania. Lee, C.M.. J.F.- Fullard, and - E. Huntington. 1988. Development of a chronic toxicity test using Chironomus riparius and the sublethal effects of trisodium carboxymethyoxysuccinate, J. Test. Eval. 8(6):482-287.
- Mc Mahan .' R . F . and C.J. ' Williams. -.1986. A reassessment of growth rate. life span, lite cycles and' population dynamics in a natural population and field- caged ~ individuals of Corbicula fluminea (Muller) (Bivalvia:
Corbiculidae). Amer. Malac. Bull., Special Ed., No. 2. pp. 151-166.
-. M2t tic e . J.S. 1979. Interaction. of Corbicula sp. with power plants. In.
Proceedings. - First National Cor bicula Symposium, J.C. Britton, ed., Texas Christian University Research Foundation Fort Worth Texas, pp. 119-138. National Research Council. 1981. Testing for effects of chemicals ots
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ecosystems. National Academy Press. Washington, D.C. Nalson, M . K. . . C.O. Ingersoll, and F.J. Dwyer. 1988. Proposed guide for conducting solid-phase sediment toxicity tests with freshwater
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invertebrates. Draft No. 2, ASTM Comm. E-47. 73
NPSP. :1989. - Nonparametric Statistical Package. Department cf Statistics and Statistical Censulting Laboratory. VPIASO. Blacksburg. VA. Shema. R.-L.. W.R. Cody. 0.J. Kenderas. M.R. Noel. M. F. Davison. 0.M. Styborski.
.J.M. McMullen. B.C. Reuter. D.S. Cherry and J.V. McIntire. 1988. Annual environmental report non-radiological Duquesne Light Company Beaver Valley Power Station Units 1 and 2. Shippingpor . Pennsylvania.
Shema. R.L. . V.R. - Cody Q.J. Kenderes. M.F. Davison. M.R. Noel. 0.M. Styborski. D.S.-Cherry, and J.W. McIntir e . 1989. Annual environmental- report non-radiological Duquesne Light Company Beaver Valley Power Station Units 1 and
- 2. Shippingport. Pennsylvania 145 pp.
United States Environmental Protectica Agency. 1973. Biological. Field and Laboratory Methods for Measuring the Quality of Surface Waters and Effluents. -Edited by C.I. VEber. US EPA. Cincinnati.'0H. 157 pp. United States Environmental Protection Agency. 1985. Methods for Measuring the Acute Toxicity of Effluent to Freshwater and Marn.e Organisms. Edited by W.H. Peltier and C.I. Weber. US EPA. Cincinnati. CH. 216 pp. United States Environmental Pr'otection Agency. 1985. Short-Term Methods for Estimating the Chronia. Toxicity of Effluents and Receiving Waters to Freshwater Organisms. Edited by W.B. Horning and C.I. Weber. US EPA. Cincinnati OH. 162 pp. United States Environs stal Protection Agency. 1989. Short-Tern Methods for Estimating the Chronic Toxicity of Effluents and Receiving Waters to Freshwater Organisms. C.I. Weber et al., editors. US EPA. Cincinnati. OH. 249 pp. r i 74 l-r-}}