ML20081C504
| ML20081C504 | |
| Person / Time | |
|---|---|
| Site: | Salem, Hope Creek, 05000000 |
| Issue date: | 02/29/1984 |
| From: | Public Service Enterprise Group |
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| ML20081C502 | List: |
| References | |
| NUDOCS 8403140117 | |
| Download: ML20081C504 (647) | |
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{{#Wiki_filter:. Salem 316(b) Desu;nstrction n SALEM GDIERATING STATION 316(b) DEMONSTRATION lO i ! NPDES Permit No. NJ0005622 i NRC Operating Licenses DPR-70 and DPR-75 I NRC Docket Numbers 5-272 and 50-311 t l Prepared by l j Public Service Electric and Gas Company 80 Park Plaza Newark, New Jersey 07101 February 1984 1 'O 8403140117 840305 PDR ADOCK 05000354 A PDR
, Salem 316(b) Dessantretica SALEM GENERATING STATION 316(b) DEMONSTRATION Page
- 1. EKECUTIVE SUMMAPT 1.1-1 1.1 Regulatory Background 1.1-1 1.2 The Delaware System 1.2-1 1.3 The Salen Station 1.3-1 1.4 The Salem Study Program 1.4-1 1.5 Life-History Summaries for the Studied Species 1.5-1 l.6 Entrainment and Impingement 1.6-1 1.7 Impact Assessment 1.7-1 1.8 Alter. u tives 1.8-1 1.9 The Best Technology Available at Salem 1.9-1
- 2. THE DELAWARE STSTEM 2.1-1 2.1 Morphology 2.1-1 2.2 Hydrology 2.2-1 2.3 Water Quality 2.3-1 2.4 Aquatic Habitats 2.4-1
. 2.5 Aquatic Life 2.5-1 2.6 Community Ecology 2.6-1
- 3. THE SAL 1!M STATION 3.1-1 3.1 The Site and Its Surroundings 3.1-1 3.2 Salem Station 3.2-1 3.3 Cooling Water Systems 3.3-1 3.4 operation of Salem Station 3.4-1
- 4. THE SALEM STUDT PROGRAM 4.1-1
- 4.1 Selection of Study Organisms 4.1-1 4.2 The Study Objectives and Plan-of-Study 4.2-1 4.3 Entrainment and Impingement Abundance and Survival Studies 4.3-1 4.4 Field Studies 4.4-1 j 5. LIFE-HISTORT SUMMARIES FOR THE STUDIED SPECIES 5.1-1 5.1 The Macroinvertebrates 5.1-1 5.2 The Fish 5.2-1
Salem 316(b) Dem:nstration CONTENTS (Continued) Page O
- 6. ENTRAINMENT AND IMPINGEMENT 6.1-1 6.1 Entrainment 6.1-1 6.2 Impingement 6.2-1 6.3 Estimates of Relative Cropping for Target Species 6.3-1 6.4 Potential Biases in Impingement and Entrainment Estimates 6.4-1 i 7. IMPACT ASSESSMENT 7.1-1 1
7.1 Criteria for Assessing Impact 7.1-1 7.2 Synopsis of the Environmental Setting 7.2-1 l 7.3 Community-Level Effects 7.3-1 7.4 Ecosystem-Level Effects 7.4-1
- 8. ALTERNATIVES 8.0-1 l
8.1 Selecting Alternatives for Detailed Study 8.1-1 8.2 Retaining Current Ristroph Traveling Screens, Fish-Return System, and Planned Outage Schedule 8.2-1 8.3 Dredging 8.3-1 l 8.4 Installing Fine-Mesh Screens 8.4-1 8.5 Improving the CWS Fish-Return System 8.6 Revising Planned Outage Schedules 8.5-1 8.6-1 lll 8.7 Reducing Flow 8.7-1 l 8.8 Increasing CWS Intake Size 8.8-1 8.9 Installing Passavant or Cogenel Intake and Screens 8.9-1 l 8.10 Retrofitting Closed-Cycle Cooling 8.10-1 8.11 Building a Second Intake 8.11-1
- 9. THE BEST TECHNOLOGY AVAILABLE AT SALEM 9.1-1 9.1 Criteria for Identifying the Best Available Cooling Water Intake Technology 9.1-1 9.2 The Best Cooling Water Intake Technology at Salen 9.2-1 9
l l
Salem 316(b) Demonstration O SECTION 1: EXECUTIVE
SUMMARY
.O . !O
Salem 316(b) Demonstration SECTION 1: EXECUTIVE
SUMMARY
Pane 1.1 REGULATORY BACKGROUND 1.1-1 1.2 THE DELAWARE SYSTEM 1.2-1 1.3 THE SALEM STATION 1.3-1 1.4 THE SALEM STUDY PROGRAM 1.4-1 1.5 LIFE-HISTORY SUMMARIES FOR THE STUDIED SPECIES 1.5-1 1.6 ENTRAINMENT AND IMPINGDfENT 1.6-1 1.7 IMP).CT ASSESSMENT 1.7-1 1.8 ALTERNATIVES - 1.8-1 1.9 THE BEST TECHNOLOGY AVAILABLE AT SALEM 1.9-1 O t u l O
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Salem 316(b) Demsnstration 1.1 REGULATORY BACKGROUND ( The Atomic Energy Commission (AEC), now the Nuclear Regulatory Commis-sion (NRC), authorized the construction of the Salem Nuclear Generating Station on September 25, 1968. Its decision followed a public hearing and detailed consideration of all aspects of the facility by the Atomic Safety and Licensing Board. Construction began immediately, and while it was underway, Congress passed the National Environmental Policy Act of 1969 (NEPA). Pursuant to NEPA, a number of governmental agencies in the early 1970s participated in a more. intensive review of the likely environmental effects of Salem station. This work resulted in the publication of a Final Environmental Statement (FES) by the Atomic Energy Commission in April 1973. Among the matters considered were the possible effects , of zooplankton and fish losses due to impingement and entrainment at Salem's cooling-water intake structures--the subject of this Demonstra- ! tion. The Commission concluded: The small losses of zooplankton, attributable to stresses imposed during passage through the cooling-water system (i.e., + entrainment), will not' be measurable in terms of ef fects on the biomass or productivity of adjacent waters. Similarly, water-intake screen losses of fish [i.e., impingement] are judged to be small and insignificant in terms of potential . impact on the aquatic ecosystem. (AEC 1973) - n-
- s_, The AEC also considered whether a closed-cycle cooling system with cooling towers might in any sense " improve" environmental effects of Salem's original cooling system, and whether it could do so at a reasonable cost. It concluded as follows:
On balance, a review of the applicant's proposed condenser cooling system design shows that only negligible environ-i mental impacts are anticipated to occur. On this basis, an additional present value cost of $182.5 million to further
- reduce an already negligible environmental impact cannot be justified, particularly in view of potential ef fects
, associated with salt drift. This alternative is therefore considered inferior to the proposed action. (AEC 1973)
To verify that these expectations were correct, the AEC followed recommendations made in comments by the Environmental Protection Agency
'(EPA) and the Department of the Interior, and required Public Service Electric & Gas Company (PSE&G) to continue the baseline studies begun in 1968, and to monitor entrainment and impingement during operations i at the' site (AEC 1973). The New Jersey Department of Environmental Protection (NJDEP) commented on other aspects of the environmental statement, but not on AEC's conclusions regarding impingement or entrainment (AEC 1973).
Less than 6 months before the AEC completed its FES. Congress passed C_]J - the Federal Water Pollution Control Act (FWPCA) of 1972. With con-struction well uncerway, this new law for the first time required 1.1 Sslem 316(b) Demonstration "that the location, design, construction, and capacity of cooling-water intake structures reflect the best technology available for minimizing adverse environmental impact." In response to this new requirement h and to issucs considered during preparation of the FES, PSE&G undertook to examine potential means of reducing impingement and entrainment losses at Salem's cooling-water intake, while continuing its data-gathering activities. PSE&G concluded in 1976 that the construction and installation of Ristroph-equipped vertical traveling screens and a bi-directional fish-return system was compatible with the original ' intakes approved by AEC, that it could produce sizable reductions in cropping of important fish species, and that it would not impose unacceptable costs. Accordingly, PSE&G began implementing these modi-fications to the original design and completed them during the summer of 1978. Subsequent studies demonstrate that these modification; have in fact reduced the cropping of such important species as white perch and weakfish (AEC 1973) by about 60 and 30 percent, respectively. Also during 1978, EPA, NJDEP, and a number of other governmental agencies participating in a Technical Advisory Group began to work with PSE&G to develop a plan for demonstrating whether PSE&G's intake structures complied with the new requirements of the Federal Water Pollution Control Act. Pursuant to agreements reached, PSE&G embarked on a more detailed study program spanning 5 years and including the extensive field and laboratory investigations described in Section 4 of this Demonstration. Together with the earlier environmental monitoring, begun in 1968, these investigations have produced a total of 15 years of observations supporting the conclusions stated here. This information has been analyzed extensively using accepted methods, including state-g of-the-art mathematical techniques. The purpose of this report is to set forth the information resulting from these studies and to present the conclusions of the investigators regarding its meaning. To sumirize, the investigators have concluded that the evidence they have collected supports the earlier expectations of the AEC. The pre-sent intake structures at Salem do not appear to be having an " adverse environmental impact" on the ecology of the Delaware estuary, even though sometimes large numbers of larval and juvenile fish are cropped due to impingement or entrainment. The substantial costs of retro-fitting alternative intake structures, operating practices, or cooling systems that could further reduce cropping are out of all proportion to the environmental significance of those reductions. Thus, the present intake system represents the "best technology available" for Salem Generating Station. O 1.1-2
Salem 316(b) Demsnstration 1.2 THE DELAWARE SYSTEM q-b The Delaware system encompasses a variety of habitats ranging from fresh water in the Delaware River north of Trenton, New Jersey, through tidal fresh water and tidal brackish water in the lower Delaware River and upper Delaware Bay, to marine water in the lower Delaware Bay and the contiguous Middle Atlantic Bight of the Atlantic Ocean. In size and volume, this system is very large, whether one is speaking in absolute or relative terms. The Delaware River stretches 595 km (369 mi) with numerous sizable tributaries such as the Lehigh and Schuylkill rivers. The Delaware Bay extends another 30 km (50 mi) to the Atlantic Ocean, , and reaches a width of 43 km (26 mi). Tidal flows associated with the Bay extend at least 40 km (24 mi) into the Atlantic Ocean. The total freshwater flow into Delaware Bay averages 644.7 m3/sec. Total volume of the Bay alone is approximately 12 km3 In addition, there is a net flow into the Delaware estuary of 69 m3/sec from the Chesapeake Bay by means of the Chesapeake and Delaware (C&D) Canal. In the vicinity of Salem station, the average tidal flow at Trenton is about 11,320 m3/see and the average downstream freshwater flow at Trenton is over 339 m3/sec. For purposes of comparison, the maximum withdrawal rate for Salem's service and cooling water systems is <2 percent of the tidal flow past its intake. Three factors that greatly affect the types of organisms present and their distribution within this system are its salinity, temperature, and dissolved oxygen patterns. Salinity in the Delaware system ranges O> from fully fresh in Delaware River to fully saline on the continental shelf off the mouth of Delaware Bay. This salinity gradient moves up and down the system according to the volume of freshwater flow into the estuary, which in turn varies with seasonal and annual rates of precip-itation. Similarly, temperature gradients develop in the system, being most apparent in summer and winter. The large volumes of ocean water entering the Bay on each tidal cycle are less subject to seasonal tem-perature extremes than the Delaware River waters to the north, and tend to moderate the temperature regime of the lower Bay. In summer, water l temperature decreases from the head of the Bay southward; in winter it increases. Delaware system waters are generally well-oxygenated, with higher dissolved oxygen levels in winter than in summer. In summer, there is 'a noticeable sag in oxygen levels in the Philadelphia area
- caused by industrial wastes and municipal sewage effluents. Dissolved l oxygen levels typically recover within 20-40 km downstream.
The vast majority of life forms in the Delaware system are energy pro-ducers: vascular plants and phytoplankton that through photosynthesis convert sunlight and other materials into stored energy to be used by other " consumer" organisms. These consumers consist of microbes (that feed primarily on decaying producers, releasing nutrients and acting as food for other consumers), zooplankton (small animal life transported primarily by water. currents), benthic invertebrates (which live in or on bottom sediments), and, at the top of this food chain, fish. l 1.2-1
Salem 316(b) Demonstration More than 90 fish species have been observed near Salem station; these include migratory and resident species. The dominant migratory species visiting the area of Salem include six species studied in detail for h this Demonstration: weakfish, spot, Atlantic croaker, shad, blueback herring, and alewife. Two within-estuary migrants were also studied: white perch and bay anchovy. People use the Delaware system for transportation and a variety of recreational, commercial, industrial, and municipal purposes. The human activities most germane to this Demonstration are those involving the local commercial and recreational fisheries. The species of prin-cipal interest to these fisheries are studied in this report. O O 1.2-2 ;
Salem 316(b) Demonstration l 1.3 THE'S_ALEM SE TION On December 13, 1966, PSE&G made application to the Atomic Energy Com-mission (now the Nuclear Regulatory Commission) for permission to con-struct a nuclear generating station. In 1968, following AEC review and public hearings by the Atomic Safety and Licensing Board, construction l pescits were issued and actual construction began at Artificial Island on the eastern shore of Delsware Bay in Salem County, New Jersey, about 80 km (50 mi) northwest of the mouth of the Bay and 48 km (30 mi) south-west of Philadelphia. Construction of Salem station progressed in the late 1960s and early 4 1970s, a time when heightened public concern for and awareness of the environment resulted in the passage of several new statutes. Among these were the -National Environmental Policy Act of 1969, which requires federal decision-makers to consider and report the potential environ-mental consequences of their actions, and the Federal Water Pollution Control Act of 1972, which for the first time required cooling water i i intakes to reflect the "best technology available" for minimizing adverse environmental impacts. NEPA's requirements were applied to, Salem, and were satisfied when AEC determined, on the basis of an envi-ronmental impact statement, that the station's effects on the environ-
- . ment had been mitigated properly and were acceptable. Construction on Unit No. I was completed and commercial operation began in 1977.
The U.S. Environmental Protection Agency began to implement cooling QL' water intake requirements with respect to Salem station in 1978 when it requested PSE&G to perform a multiyear Section 316(b) study to assist the Agency in determining the best technology available for the cooling i water intakes at Salem. Meanwhile, PSE&G voluntarily undertook numerous improvements to its original cooling water intakes, and completed con-struction of Unit No. 2, which became operational in 1981. Sales station is locat(d in Lower Alloways Creek Township, New Jersey, on a site bordered by Delaware River on two sides and by extensive marshes and uplands on the remaining two sides. Together with the adjacent Hope Creek station, the site covers 740 acres of land. There is little natural vegetation on the site, and what does exist is mostly reed grass. { Salem station was located next to Delaware Bay for a very important ' reason. All steam-electric generating stations require cooling water to l operate, whether they are fueled by coal, oil, or nuclear power. These facilities use their fuel to produce heat, which converts water to steam that drives a turbine generator. To turn the generator, steam pressure at the' outlet of the turbine must be an:h lower than on the inlet side. This is accomplished by cooling the at am with water as it exits the turbine,.thereby condensing it and reo..ing its volume. The colder the
- cooling water, the more ef fectively it condenses the steam, the greater the pressure difference across the turbine, and the more efficiently electricity is generated. Salem was designed and constructed to use O. relatively low-temperature, once-through (open-cycle) cooling water 'V directly from Delaware Bay, as opposed to relatively higher-temperature recirculated (closed-cycle) cooling water.
1,3-1
Sclem 316(b) Demonstretion The main cooling water systems (CWS) at Salem are called the circulat-ing water systems. There are two systems, one for each unit. They share a shoreline intake structure on the southwest edge of Artificial h Island, and consist of piping, steam condensers, and a submerged dis-charge to the Delaware Bay approximately 180 m offshore. The intake structure was altered at considerable expense in the middle and late 1970s to incorporate Ristroph vertical traveling screens, which are operated continuously to minimize the time organisms may be impinged. Impinged organisms slide down the screens as they travel above intake water level, and are caught in water-filled buckets at the base of each ascending screen panel to prevent re-impingemenc. The buckets are emptied into sluiceways which return fish to the Bay north of the CWS intake on flood tide, and south of the CWS intake on ebb tide, to pre-vent re-impingement. Salem contributes about 10 percent of the total electrical generating capacity of the PSE&G system, which serves about 1,700,000 electricity consumers. Because it is a nuclear facility with relatively low operat-ing costs, Salem functions most economically as a baseload plant, i.e., it should operate at maximum capacity whenever it can. Since it also provides a substantial portion of PSEEG's overall generating capacity, it is important that it operate efficiently during annual peak electri-cal demand in July , August , and September. At that time, the opera-tional cost of producing electricity at Salem is $12/MWh, compared to an incremental cost on the PSE6G system of $129/MWh. At average full-power operation, Unit No. I has produced 1,050 MWe; Unit No. 2 has produced 1,063 MWe in the study period. h 9 1.3-2
i Salem 316(b) Dem:nstretion 1.4 THE SALEM STUDY PROGRAM l
- Mg This Demonstration reflects the results of 15 years of environmental studies conducted by PSE&G and its consultants on the potential aquatic effects of Salem statica on the Delaware system. The most recent of these studies, conducted from 1978 through 1983, focused on certain
" target" species selected for study by the U.S. Environmental Protection
_ Agency, the New Jersey Department of Environmental Protection, the Delaware Department of Natural Resources and Environmental Control, the Delaware River Basin Conunission, the U.S. Fish and Wildlife Service, the National Marine Fisheries Service, and the Nuclear Regulatory Com-mission.~ These agencies comprised a Technical Advisory Group, which monitored the preparation of the study plan and its performance. The target species consisted of nine fish species (weakfish, bay anchovy,-white perch, striped bass, blueback herring, alewife, American shad , s po t , and Atlantic croaker) and two macroinvertebrates (Neomysis americana and Gammarus spp.). These species are not simply a represen-
- tative cross section of species found in Delaware Bay; rather, they
- are a set of spec ~ies especially selected to indicate effects that might result from Salem operations. They include species with relatively high potential for involvement with Salem, species of particular commercial
' and recreational value, species important to the food web and overall l ecology of the Delaware system, and species of particular regulatory concern.
The goal of the Salem studies was to determine what effect, if any, O-- the o, ratten ef Sa1em s cee11n. water intaxe has en the ecete87 ef the source waterbody. The studies pursued this goal by gathering two types of information on the target species: (1) data on the numbers of each spe'cies lost to entrainment and impingement at Salem, and (2) data on the nature of the source populations such as size, distribution, age composition, reproduction, mortality, growth, and exploitation. The Plan-of-Study under which these investigations were conducted was revised several times to improve the usefulness and accuracy of the information gathered, based on increased experience with the tasks at hand. In general, it provided the framewcck for an extensive sam-pling program at Salem station and throughout Delaware estuary. Trained biologists employed in data gathering, interpretation, analysis, and literature reviews for this project have worked closely with engineers,
- statisticians, and computer programmers to evaluate the results. The
- . entire study generated thousands of samples for analysis in this Demon-i stration. In addition, laboratory tests and exhaustive literature reviews were conducted to assure the gathering of all reasonably avail-able information. The results of these investigations are summarized in Sections 5, 6, and the appendixes of this document; their meaning is analyzed in Section 7. Procedural methods for the Salem studies are described briefly in Sections 4.3 and 4.4; complete explanations are provided in Appendix I.
O 1.4-1
Salem 316(b) Demonstration 1.5 LIFE-HISTORY SUMMARIES FOR THE STUDIED SPECIES
/~T
\w I (The species studied .for this Demonstration are amocg those most involved with Sales station. Even so, most of these species use the Delaware estuary,- or that portion of it near Salem station, only during specific life stages or time periods. Anadromous fish species--such as striped bass, American shad, alewife, and blueback herring (which spawn in fresh
' water)--and spot, Atlantic croaker, weakfish, and bay anchovy (which spawn in marine and/or brackish water) most commonly use the estuary for spawning or as a nursery area for their young. Some older individuals of several species overwinter in the lower Bay. Only the white perch can be considered a permanent inhabitant of the Delaware River system.
Four of these species--bay anchovy and the three anadromous clupeids (alewife, blueback herring, and American shad)--are pelagic, schooling, typically planktivorous fish. Except for shad, their principal value to man in the Delaware estuary is as prey for species of commercial or recreational importance.- American shad both contributes to the estua-rine forage base and supports a small fishery within the Delaware River. Three other fish species (weakfish, spot, and Atlantic croaker) are predatory members of the Sciaenid (drum) family. These marine species use estuaries primarily as nurseries and, to a much lesser extent, as everwintering areas. All three support important commercial and recre-ational fisheries along the Atlantic coast, although spot is generally not. fished in the Delaware. The Delaware estuary is at the northern
- i. extreme of the spawning range for spot and croaker. The larval stages are all planktivorous, whereas the juveniles and adults feed on abundant
' invertebrates and fish.
The other two fish species (white perch and striped bass) are both mem-bers of the Percichthyid (temperate bass) family. White-perch are life-long estuarine inhabitants, whereas the anadromous striped bass uses estuaries primarily for spawning and nursery. In the Delaware, striped bass spawning occurs only in the C&D Canal with few young using the ,
- Delaware River as a nursery.. Both species are planktivorous as larvae ,
and are predators of fish and macroinvertebrates as adults. Both have contributed to commercial-and recreational catches in the Delaware f system. The macroinvertebrate species included in the study, Neomysis americana - and the Gammarus tiarinus group, are among the many species of zoo-r plankters that function collectively as an important trophic link in l the estuaries and nearshore ocean along the eastern United States from i the St. Lawrence River to -Florida. These species are both primary and ! secondary consumers, feeding on detritus, phytoplankton, zooplankton, and aufwuchs. They, in turn, are prey for other invertebrates and fish. Many of these zooplankters evidence seasonal movement between estuaries and' adjacent coastal waters. Within the Delaware estuary, the distribu-tion of N ionysis and Gammarus is controlled largely by salinity. During ! winter and spring, when high freshwater flow pushes the salt front down the estuary, Gammarus move into the reach of the Delaware estuary near
.( }
o l 1.5-1 l' c
Sclem 316(b) Demonstration l l Salem. As freshwater flow subsides and summer progresses, euryhaline-marine species such as Neomysis increase in abundance and the Gammarus population shifts back upstream. 1 l 1 l 1 1 l O O l I i O 1.5-2 i
r Salem 316(b) Demonstrction 1.6 ENTRAINMENT AND IMPINGEMENT Entrainment and impingement are the two mechanisms by which Salem's intake structure might affect aquatic life in Delaware Bay. When water is withdrawn from a source waterbody, organisms too small to be excluded by the-intake screens can be drawn through the station's cooling system and returned via its discharge. This is called "entrainment." Organ-isms too large to fit through the intake screens, but too small (or lacking in swimming abili~ty) to avoid the intake current, may be pressed or." impinged" against the intake screens until they can be removed and returned to the waterbody. Some organisms tl.at are entrained or
-impinged die as a result. Others are able to withstand the stresses
-involved and continue their existence after being returned to the source waterbody.
To provide a basis for evaluating the significance of entrainment and impingement losses at Salem, PSE&G and its consultants have performed extensive calculations and analyses based on the sampling data and other
-information developed during the Salem studies (Section 4). For target species subject to entrainment, they calculated typical cooling water densities for various periods and the rates at which the different life stages involved survive. From this information, it was possible to estimate entrainment losses as a function of cooling water volume pumped. By multiplying the rate of typical entrainment losses during each period by probable cooling water flow during the period and sum-ming the results, it was possible to calculate annual estimates of s entrainment losses to each of the target species subject to entrainment.
A full explanation of these esiculations and a presentation of their results appears in Section 6.1. - Similar analyses were performed based on the impingement data. In , summary, data from the impingement abundance and survival studies were used-to estimate impingement loss. rates per unit volume flow by month ! and specimen age. The losses for each period and life stage were then summed using probable full-power cooling water flows during each inter- ! val to estimate annual cropping during a typical year. Section 6.2 contains an explanation of these calculations and a presentation of their results; details are presented in Appendix I. Estimates of entrainment and impingement losses are of little use unless they relate to various aspects of the source populations. Since it was possible to express such relationships mathematically in several ways, PSE&G and its consultants used mathematical models to calculate
" conditional mortality rates," equivalent adult losses, production fore-l gone, or lost reproductive potential, where possible, for the target species. These indices assist in assessing population-level effects when evaluated in conjunction with other necessary information concern-f ing a particular species. These indices are summarized in Section 6.3.
The results and their meaning are detailed in Section 7. l l' 1.6-1
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. Solen 316(b) Demonstration
-1.7- JMPACT ASSESSMENT Many of the biological communities in the Delaware estuary are not affected at all by the operation of Salem station. The locations of
- many of these communities either limit or preclude direct involvement with the-Salem station cooling water system intakes. Included in this
, category are'all biological communities in the freshwater streams trib-
- utary to the estuary. Detritus and organisms in the water discharged from these streams contribute to the food base of the estuary. Organ-isms in these streams also provide food for certain life stages of fish species that migrate through the estuary from coastal marine waters.
Also included are the vascular plant community and associated animal communities in the extensive marsh / littoral zone habitat along both margins of the estuary. Detritus and organisms flushed from these marshes by tidal flows make a major contribution to the food base of consumer communities in the open water (pelagic) zone of the estuary. The benthic invertebrate community which lives in or on the bottom of
- the pelagic zone, and pelagic freshwater and marine organisms that live upstream or downstream in the tidal portion of the system, but which cannot survive the oligohaline condition that prevails most of the time in the vicinity of Salem (Figure 2.3-2), are also included in this category.
Other communities experience negligible or very low relative losses at Salem station, even though they are the most highly involved numeri-cally. _ These include the pelagic, euryhaline microbial decomposer,
~
phytoplankton, nano- and micro-zooplankton communities (Figure 7.2-1). By the mid-1970s, findings of no appreciable impact based on extensive
- studies at numerous operating power plants were sufficient to cause federal interagency technical- committees to assign " low potential impact" status to these lower trophic' level communities. More recent studies confirm that this status is appropriate for those lower trophic level communities, and also for the macrozooplankton community at sites such as Salem on large, dynamic estuarine systems. Two of the desig-nated target species for this Demonstration, Neomysis americana and 0
~
Gammarus spp. , are numerically prominent components of the macrozoo-plankton community. Both are habitat sharers, meaning that they occur both as benthos and plankton in. proportions that vary as a result of - diurnal migrations. Estimates of the conditional mortality rate due to entrainment for the different seasons of the year range from 0.1 to I - 3.0 percent for Gammarus spp. and from 0.4 to 2.9 percent for Neemysis americana (Section 6.3). These quite low values are biased high to the extent that their computation included only the component of the popu-lations in the macrozooplankton, and did not include either the benthic component of the total populations or the transport of these organisms into and out of the modeled study area (rkm 64-97). J The absence of apparent impact due to entrainment (they are too small to be impinged)- for this group of communities is usually attributed to a combination of factors such as short generation time, high reproductive capacity, and high abundance and dispersitivity, which rapidly ef fect replenishment of abundance. Additional factors applicable to Salem are
-O- quite high entrainment survival during much of the time for many of the 1
1.7-1
Salem 316(b) Dem:ncer.ttion component species in these communities and the fact that the instanta-neous rate of cooliag water entrainment is a very small portion (<2 per- llh cent) of the total average tidal flow past the intake (Section 7.3). Fish in the pelegic zone of the oligohaline reach of the estuary are
< also subject to involvement with' the Salem cooling water system. Nine of the eleven designated target species for this Demonstration are fish.
The bay anchovy--a small, secondary consumer, forage species--is by far the most involved species' numerically at all life stages. Because of its _ ecological functions, the most appropriate mathematical technique
' for~ assessing cropping of bay anchovy is a " production foregone" cal-culation. This estimates the possible reduction in accumuiated biomass
,1 available to the ecosystem. Based 'on this analysis, cropping of bay anchovy in the study area is estimated to be approximately 10 percent.
This estimate is biaseC high in that the computations include only the organisms in the study' area, and do not include exchange between the
. Delaware Bay and adjace~ coastal waters. Other conservative assump-tions of this s.nalysis are set forth in Section 6.3. Bottom trawl cieches of anchovy near Salem station indicate no particular trend of abundance in any direction for the period 1970 through 1980 (Appendix XII, Section 4).
?hst other studied species of fish are much less involved with the Salen co'oling water system. In most cases, just one or a feu life stages are
? involved. Bottom trawl catch data near Salem for the period 1910-1980 irdicate no particular changes in abundance trends for these species since Salen began operation in 1977. The estimated cropping rates due co entrainment and/or impingement are quite smt.11 for the most part com-lll pared to other known sources of exploitation.
In summary, the evidence collected and examined during this study suggests that the continued operation of Salem's existing cooling water ictske system will not cause any significant adverse environ-mental impact to aqustic populations in the Delaware estuary. k
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Salem 316(b) Demsnstretion 1.8 ALTERNATIVES PSE&G and its consultants have surveyed more than 40 possible alterna-tive intake designs and practices as part of this study. Each alter-native was evaluated preliminarily as to its technical feasibility and applicable engineering considerations, its ability to reduce cropping deze to entrainment and impingement, its other environmental ef fects, and its cost factors. The results of those general evaluations are presented in Appendix XIII. In general, many of the alternatives were found to be practically infeasible, to offer no prospect for reduced cropping, to have undesirable environmental side effects, to be extremely costly, or to have severs 1 of these qualities simultaneously. Such alternatives were dismissed from more detailed consideration in this Demonstration. At the completion of this process,10 alternatives remained that were considered either promising, or about which insufficient site-epecific information and analyses could be developed within the scope of the preliminary Appendix XIII inquiry to draw meaningful conclusions. Each alternative is brought forward for more detailed examination in Section 8 of this Demonstration. These alternatives include:
- 1. Retaining operation of the existing Ristroph CWS traveling screens and fish-return system
- 2. Dredging the CWS intake approach channel
) 3. ' Installing fine-mesh CWS traveling screen panels
- 4. Improving the existing CWS fish-return system
- 5. Revising the planned schedule for refueling
- 6. Reducing CWS cooling-water flow volume by installing two-speed pumps
- 7. Increasing the size of the CWS intake
- 8. Installing Passavant or Cogenel screens
- 9. Retrofitting a closed-cycle cooling system
- 10. Constructing a second CWS intake for Unit No. 2 These alternatives are discussed in Sections 8.2 through 8.11, respec-tively . Separate subsections present engineering and technical con-siderations, likely effects on entrainment and impingement cropping, other environmental ef fects, and cost. This information is then weighed and compared against the appropriate criteria for selecting the "best technology available?' in Section 9.
v 1.8-1
Salem 316(b) Demonstration , 1.9 THE BEST TECHNOLOGY AVAILABLE AT SALEM > p e Under the Clean Water Act, the "best technology available" is the least expensive one that either:
- 1. reduces significant adverse environmental impacts associated with the intake structure to the point that they cease to be significant, or i
- 2. reduces such environmental effects to the point that further
, reductions are out of all proportion to the anticipated environmental gains. Several.of the intake alternatives considered cannot satisfy either of these criteria because they have no demonstrable ability to reduce , cropping (rnd hence could not reduce any significant adverse environ-mental impact), yet they involve substantial expenses and other undesir-able environmental effects. These alternatives include dredging, fine-mesh screens, increasing the size of the intake, building a second intake, and installing Passavant or Cogenel screens. j Five other intake alternatives have demonstrated ability to reduce entrainment - or impingement cropping of some or all species. They are: retaining the existing Ristroph vertical traveling screens and fish-return system, revising the refueling outage schedule, making additional improvements to the existing fish-return system, reducing cooling-water flows, and the retrofit construction of a closed-cycle cooling system. Of these alternatives, it is clear that the existing Ristroph traveling
; screens and fish-return system is the "best technology available."
As summarized earlier, conservative estimates of relative cropping of 1 studied species show low involvement with. Salem station. The existing intake structure and operation has .already reduced cropping for the species most involved with Salem from the levels existing when the AEC
- found no significant environmental ef fects. The existing intake is not having an adverse environmental impact on the ecology of the Delaware f
estuary. Further cropping reductions from these low levels are not likely to be of ecological significance, yet they involve tremendous
. costs, potentially important environmental side ef fects, and technical and engineering difficulties. In contrast, continued operation of the existing intake system involves no technical difficulties, no other l
adverse environment ', ef fects, and is the least costly alternative available. It is the best available technology for Salem Generating
' Station.
~
1.9-1 i
Solen 316(b) Demonstration z LITERATURE CITED: SECTION 1 i
.O i Atomic Energy Commission (AEC). 1973. Salen Nuclear Generating i' Station, Final Environmental Statement, April 1973. AEC, Washington.
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Salem 316(b) Demonstration l i O 4 s SECTION 2: THE DEIJ. WARE SYSTDi O O - (
Salem 316(b) Demonstration SECTION 2: THE DELAWARE SYSTEM Page LIST OF TABLES LIST OF FIGURES 2.1 MORPHOLOGY 2.1-1 2.2 HYDROLOGY 2.2-1 , 2.3 WATER QUALITY 2.3-1 2.3.1 Salinity 2.3-1 ' 2.3.2 Temperature 2.3-2 2.3.3 Dissolved Oxygen 2.3-3 2.4 AQUATIC RABITATS 2.4-1 2.5 AQUATIC LIFE 2.5-1 2.5.1 Producers 2.5-1
- 2. 5.1. ] Vascular Plants 2.5-1
( ). 2.5.1.2 Phytoplankton 2.5-2 2.5.2 Consumers 2.5-3 2.5.2.1 Microbes 2.5-3 2.5.2.2 Zooplankton 2.5-3 2.5.2.3 Benthic Invertebrates 2.5-5 2.5.2.4 Fish 2.5-7 2.5.3 Endangered, Threatened, or Special-Status Species 2.5-9 i 2.6 COMMUNITY ECOLOGY 2.6-1
- 2.6.1 Energy Flow and Trophodynamics 2.6-1
! 2.6.2 Human Use of the Delaware System 2.6-3 2.6.2.1 Recreational Uses 2.6-3 2.6.2.2 Commercial, Industrial, and Muncipal Uses 2.6-6 2.6.2.3 Transportation 2.6-7 2.6.2.4 Water Supply 2.6-9 LITERATURE CITED l
' Salem 316(b) Demsnetration LIST OF TABLES:
SECTION 2 Number , Title I i 2.1-1 Characteristics of the east and west shores of Delaware estuary. 2.2-1 Drainage areas and gauged river flow of streams tributary to Delaware River and Bay. 2.5-1 Fishes collected from the Delaware River and tidal tributaries near Artificial Island annually during January 1970 through December 1976. O O
.. . .- - . ._ _ - - _ . -= .. .
Salem 316(b) Dem:nstration LIST OF FIGURES: SECTION 2 Number Title 2.1-1 Location of the Delaware River Basin. 2.1-2 The Delaware estuary including major tributaries and tidal wetlands. 2.1-3 Configuration of the Delaware estuary. 2,2-1 Semimonthly mean freshwater flow rate of the Delaware River at Trenton, New Jersey, 1970-1982. 2.2-2 Delaware estuary in the vicinity of the Salem station. 2.3-1 Seasonal patterns of salinity distribution in the Delaware estuary. 2.3-2 Semimonthly mean and range of salinity and flow rates for the period 1970-1982 in the Delaware system. 2.3-3 Semimonthly mean salinity during 1970-1981, based on conductivity measurements, USGS water quality monitoring station at Reedy Island Jetty, Delaware. 2.3-4 Seasonal temperature pattern of Delaware River at Trenton and offshore coastal waters. 2.3-5 Seasonal patterns of temperature distribution in the Delaware est;uary. 2.3-6 Semisionthly mean water temperature of the Delaware River estuary from rka 0 to rka 120 during April, June, July, and September 1981.
/
, 2.3-7 Semimonthly mean water temperature during 1970-1981, USGS Water Quality Monitoring Station at Reedy Island Jetty, Delaware. 2.3-8 Mean DO concentration in the Delaware River from rka 80 to rka 212 for April-June and September- November 1980. 2.3-9 Semimonthly mean dissolved oxygen concentration during 1970-1981, USGS Water Quality Monitoring Station at Reedy Island Jetty, Delaware. 2.4-1 Conceptual diagram of habitat zones for typical estuaries
, such as Delaware estuary.
l Salem 316(b) Demonstrction Number Title 2.5-1 Relative temporal abundance of dominant benthic 9 invertebrates by substrate. 2.$-2 Hean monthly catch of blue crab per trawl haul near Artificial Island, 1971-1976. 2.6-1 Conceptual energy flow diagram for the Delaware estuary. l 1 O O
Sclem 316(b) Descastration I p 1 SECTION 2: THE DELAWARE SYSTEM The Delaware system is a continuum of environments: freshwater stream, tidal fresh water, tidal brackish water, and marine. The characteris- I tics of these environments determine temporal and spatial distribution (species composition and abundance), functional dynamics, and resili-ency of the populations and communities in this system. This section describes the physical, chemical, and biological characteristics of the aquatic environment in which the Salen Generating Station operates. More information can be found in Appendix I. 8 2.1 MORPHOLOGY 2 The Delaware River Basin encompasses an area of 36,070 km . The Dela- ) were River is approximately 595 km long from the headwaters (including 1 West Branch) to Liston Point., where it enters Delaware Bay, 79 km from ,_ the sea (Figures 2.1-1 and 2.1-2) . The River origine.tes as the East and
' West branches, on the western slopes of the Catskill Mountains in New
~ York State, which join near Hancock, New York. In these mountainous and
. heavily forested areas, three water supply reservoirs for the New York Metropolitan Area (the Cannonsville, Pepacton, and Neversink) are fed by the Delaware. From here, the River continues south to Port Jervia, New York, where it becomes the boundary between New Jersey and Pennsylvania.
It continues southwest through the Delaware Water Gap in the Kittatinny Mountains near Stroudsburg, Pennsylvania. The gorge at the Delaware , O Water Gap is approximately 5 km long, reaching a height of 427 m. Below the Gap, the_ River flows into more rolling, open country. The first major tributary, the Lehigh River, joins the Delaware at Easton, Penn-sylvania. The Lehigh has a drainage area of 3,533 kr.2 The Delaware's t largest tributary, the gehuylkill River, enters at Philadelphia, drain- . ing an area of 4,903 km The Chesapeake and Delaware (C&D) Canal connects the Delaware River, at rka 92, with the Chesapeake Bay via the Elk River. The C&D Canal is 25 km long and between 91 and 366 m wide; it is maintained at a depth of 11 m by the U.S. Army Corps of Engineers. Near Trenton, New Jersey, at rka 212, the River drops about 2.5 m . through rapids, marking its entrance into the tidal estuary. It is here that the " fall line" crosses the Delaware River. The fall line is a narrow zone of varying width that separates the rocky Piedmont geo-logical regions from the mandy Coastal Plain. Passing through Trenton, the line continues northeast to New York and Boston, and southwest to the Susquehanna River, the Chesapeake Bay, Ba.timore, Washington, and Richmond. The Delaware estuary is the result of tectonic subsidence, glaciation, and ' sea level changes that af fected the geology of eastern North Amer-ica. At the peak of the most recent glacial advance (12,000-15,000
- ' years ago), the estuary was a narrow freshwater river (Ward 1958). The .
- .. estuary was formed as the rising sea level, fed by the melting glaciers, flooded the ancestral Delaware River Valley. For the purpose of this 2.1-1
_a.____.__.__._____.__.____
Salem 316(b) Dem nstrction Demonstration, "the Delaware estuary" is defined as all tidal waters between the mouth of the Bay (a line between Cape May, New Jersey, and Cape Henlopen, Delaware (rkm 0]), and Trenton, New Jersey (rkm 212) g (Figure 2.1-2) . The estuary is 212 km long and varies in width from about 18 km at its mouth to about 43 km at the widest point of the Bay (rkm 20), after which it narrows gradually northward toward Trenton, where its width i' I ver8 approximately 2,000 km 2 O.3 km (Polis and Kupferman 1973). and has a volume in excess of 18 km 3.t Mean depth, cross section, and width of the estuary are shown in Figure 2.1-3. 2 Approxicately 668 km of tidal marshes surround the estuary, playing an important role in water exchange and retention, and is chemical and biological functions within the system (Section 2.5.1.1). Table 2.1-1 provides a description of the east and west shorelines of the estuary. "The Delaware Bay" is defined as the tidal waters between Cape May
" * *** **8 "
and Capea Henlopen totaling (rkm volume of 12 km 0),3*"compr**ise
, the aBay:
shallow storsge area on the New Jersey side, a central channel, and an area on the Delaware side characterized by alternating shoals and zones of deep vcter. An important component interactive with the Delaware estuary is the contiguous ocean water of the Middle Atlantic Bight (from Cape Cod to Cape Hatteras), which exists outside the entrance to the Delaware Bay. Whereas Pape and Garvine (1982) established that bottom ocean water from at least 40 km offshore is involved in residual flows into Delaware Bay, g Swain (1972) concluded that the lower Delaware Bay is a pass-through zone for organic matter, which settles to the bottom in the coastal waters near the Wilmington Canyon. Bottom topography of the estuary changes constantly because of current patterns generated by the interaction of tidal flow, freshwater dis-charges, wind shear, and density gradients. Composition of the bottom substrate is therefore quite variable. Sediments of Delaware Bay con-sist of fine sands, silts, and clays of light to dark gray color; sedi-ments contain abundant shell fragments in raany areas. In areas such as channels where currents are sufficient to maintain in suspension smaller and lighter particles (silt, clay, and organic matter), the bottom sur-face sediment is predominantly (90-100 percent) sand, interspersed with small percentages of silt, clay, and very little (0.2-0.37 percent) organic carbon. Swain (1972) reported that in the majority of surface sediment samples from the pelagic zone of the upper and lower Delaware Bay, the composition of the solid fraction was: sand, 50-95 percent; silt, 4-35 percent; clay, 1-25 percent; and organic carbon, 0.1-3 per-cent. In a few of the areas examined, the bottom surface sediments are composed of mostly clay and sand or mostly silt (mud) and clay. Each of those mixtures contained relatively high organic carbon, i.e., more than 1 percent for the clay-sand mixture and over 3 percent for the silt-clay mixture. Many areas of sandy and clay-sand bottom contain considerable amounts of shell fragments. There are few areas where the substrate is composed primarily of a mixture of gravel and shell fragments. g 2.1-2
Salem 316(b) Demenstration TABLE 2.1-1 CHARACTERISTICS OF THE EAST AND WEST SHORES OF DELAWARE ESTUARY (a) Reach East Shoreline West Shoreline Mauth to rka 84 Natural condition mostly; Natural condition tidal marshes that extend. mostly; tidal marshes up to 8 km in width at that extend up to 8 km major tributary estuaries in width at major tributary estuaries rka 84 to rka 93 Includes 5 km bulkhead Natural conditions; shoreline and filled narrow belt of tidal ground, and about 5 km marsh; unprotected natural marsh Reedy Island west of main channel rka 93 to rka 100 Mostly natural condition; Mostly protected tidal marsh up to I km shoreline, dredge dis-wide posal areas, large oil refinery; unprotected Pea Patch Island west of main channel rka 100 to rkm 108 Mostly protected dredge Mostly natural; narrow spoil areas and small belt of marsh; small (Ti
<k# . river communities town Ikm 108 to rkm 113 Mostly protected high Mostly protected; ground; highly dredge spoil areas; industrialized small town rka 113 to rka 119 About 50 percent pro- Protected dredge tected, mostly high ground disposal areas rka 119 to rkm 127 Natural of filled ground; Mostly unprotected little marshlands; mostly high ground; f all line l
unprotected from rkm 119 to rkm 216 l sometimes close to l shoreline i rka 127 to rkm 138 Many dredge disposal Mostly protected high areas, banks generally ground, highly indus-unprotected; unprotected trialized; large com-Chester and honds Islands munities of Marcus east of main channel Hook and Chester. (a) Adapted from U.S. ACE 1975b. j L) l t- .M N w g a- e u- e +-tf 2- - y -a- g + w v. 1i = - - e e'-+--w - --e- m - - --r'
Salem 316(b) Demcastration TABLE 2.1-1 (name 2 of 3) O Reach East Shoreline West Shoreline rka 138 to rka 143 Mostly bulkheaded; filled Mostly bulkheaded; ground; many industries small town; indus-tries; unprotected Tinicum Island west of main channel
- rka 143 to rka 151 Mostly unprotected filled Piers and bulkheads ground rka 151 to rka 164' City of Camden; mostly Naval Base and City of bulkheaded, about one- Philadelphia; piers third filled ground, and bulkheads; mostly
! remainder high; piers high ground and industry rka 164 to rka 174 About 50 percent bulk- City of Philadelphia, headed; much high ground; piers and bulkhead; 4 some fills; Petty Island, high ground; industry east of main channel, mostly bulkheaded fill; industry rka 174 to rka 180 About 50 percent natural City of Philadelphia; high ground; remcinder, mostly bulkheaded; filled marsh; little pro- high ground; industry tection; several residen-tial communities rka 180 to -rka 191 Mostly high ground, about Mostly natural high 50 percent protected; ground, largely unpro-several residential com- tected; dredge spoil munities and industry areas; unprotected banks; unprotected, marshy Mud Island west of main channel rka 191 to rka 196 Town of Burlington; mostly Town of Bristol; high ground, protected; high ground, mostly unprotected Burlington protected . Island with dredge spoil fill east of main channel rka 196 to rka 203 Unprotected bluffs; Natural shoreline, industry; small town little protection; about 80 percent high ground, remainder marsh
.-my ,a-~ _
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Sclem 316(b) Demonstration TABLE 2.1-1 (page 3 of 3) Reach East Shoreline West Shoreline rka 203 to rka 206 Natural, unprotected Heavy industry; pro-shoreline; high ground; tected filled ground unprotected Newbold Island east.of main channel J i rka 206 to rka 216 Mostly unprotected natural Mostly unprotected high ground; City of natural Trenton . O 4
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p ( NORTH CAROUNA l Public Service Electric Location of the Delaware River Basin and Gas Company (Adapted from DRBC 1975) O Salem 316(b) Demonstration Figure 2.1 l l l i
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O Chesapeake & Delaware Canal (rkm 92) k ' *
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- -- - - - _ . . . - - = - - -
Sales 316(b) Dem:nstration 2.2 HYDROLOGY O The hydrology of the Delaware system af fects the occurrence, distri-bution, and abundance of organisms both directly (as a result of net water transport, turbulent mixing, and exchange anong the system's
- components) and indirectly (as a result of its influence on such bio-logically important water quality parameters as salinity, temperature, dissolved oxygen, and turbidity). Freshwater discharge from the drain-age basin and upstream impoundments, tidal flow, wind, and salinity-induced density gradients are the major forces that characterize the hydrology of the system and result in its highly dynamic physical and chemical environment.
2 The Delaware estuary contains fresh water received from the River and i its tributaries, as well as sea water from adjacent coastal waters. In the lower Bay, river water combines with more saline ocean water, sometimes mixing, and sometimes forming a classical two-layered pat-tern. At the surf ace, the net flow tends to be seaward, especially along the Delaware shore. Near bottom, particularly in the deep chan-nels, the net flow tends to be upstream. This flow, set in motion by ocean currents as far as 40 km offshore, results in an exchange I of water between the ocean and the estuary and creates a longitudinal salinity gradient that typically extends from the mouth of the estuary to the lower Delaware River (Pape and Garvine 1982). These waters are mixed in the estuary by the wind, tides, and freshwater river discharge (Section 2.3.1).
' Delaware River discharge into the head of the estuary is measured near l the Calhoun Street Bridge in Trenton, New Jersey (rka 216), by the U.S.
, Geological Survey (USGS). For the period of 1913 through 1983, the mean annual freshwater flow was 333 m3/sec, with substantial daily variation. For example, from May 11 to 13, 1981, flow rate increased from about i 202 to 1,670 m3/sec. Semimonthly' patterns of flow (seasonal trends) for the period 1970-1982 are shown in Figure 2.2-1. Typically, mean flow rete peaks in Spril are due to spring runoff from melting snow and high levels of rainfall; subsequent discharges decline through summer and early fall, normally periods of lower precipitation. Minimum and maximum mean daily flows during the period of record were 33 m3/sec on October 31,1963, and 9,320 m3/ rec on August 20, 1955, respectively (USGS 1983). Of the total freshwater flow into tue Delaware estuary, annual average of 661 m3/sec,' approximately 50 percent (333 m3/sec) is contributed by the Delaware River at Trenton,12 percent (76.9 m3/sec) by the I Schuylkill River at Philadelphia, and the remaining 38 percent by all other tributaries combined (Table 2.2-1). Additionally, fresh and/or low salinity water enters the Delaware estuary from C&D Canal approxi-mately 10 km north of Artificial Island. A net eastward movement of water into the estuary, caused by differences in tidal height between Chesapeake and Delaware bays, was estimated to average 69 m3/sec (Pritchard and Gardner 1974). 2.2-1
Sclem 316(b) Dem:nstration Tides in the Delaware estuary are semidiurnal, with a period of 12.42 hours. The mean tidal range averages 1.3 m at the mouth of the estu-ary, generally increasing through the estuary to 2.1 m at Trenton (NOAA h 1982). In Delaware Bay, tidal range varies from cast to west, because of the deflecting force of the earth's rotation (Coriolis ef fect). Thus, on the flooding tide, water enters the E.c and is deflected to the right so that it accumulates on the New Jersey side; on the ebbing tide, water builds up on the Delaware side with the result that low tide is less pronounced there than on the New Jersey side. Therefore, the total range of tide is greater on the New Jersey side. In the vicinity of Artificial Island the mean tidal range is 1.8 m. Tidal ranges as high a; 4.3 m have been observed at Artificial Island during periods l of extreme flood and ebb conditions (FSE&G 1980). Current speed and direction throughout the Delaware estuary are pri-marily dominated by the tide. Tidal flow as measured near the Delaware Memorial Bridge (rkm 111) was found to be 11,320 m3/sec (USGS 1966). Tidal flow of this magnitude is 17 times as great as the total average freshwater flow rate into the estuary. Proceeding toward the mouth of the estuary, tidal flow increasingly dominates freshwater downstream flow; proceeding upstream from the Delaware Memorial Bridge, the ratio of tidal flow to net downstream flow becomes smaller as tidal influ-ence decreases. Surface tidal currents generally are directed along the longitudinal axis of the estuary except in nearshore areas of river bends and coves. At maximum ebbing or flooding tide, local currents at any point within the estuary may reach speeds of 1.0-1.3 m/sec (Polis and Kupferman 1973). $ In the vicinity of Salem station, morphology and bathymetry of the estuary appear to have a major ef feet on local current patterns. As shown in Figure 2.2-2, the estuary narrows just upstream from the site and makes a bend of nearly 60 degrees. More than half the river width in this area is relatively shallow water (depth of <5.5 m), whereas the remainder of the river width, including the dredged shipping chan-nel, ranges in depth to 12.2 m. The narrow upstream channel may produce greater tidal currents for both the flood and the ebb tide. Further, the bend may produce a persistent flow of near-surface water away from the inside of the bend (i.e., toward the Delaware shore), with a com-pensating deep flow toward the inside of the bend (i.e., toward the New Jersey shore) (Weston 1982). The cross-stream bathymetry, a central channel flanked by much shal-lower water, has two principal effects on tidal flow. First, the highest tidal velocities and the bulk of the tidal volume transport are found in the relatively narrow band of deep water centered on the shipping channel. Second, tidal currents in shallower water show a phase lead over those in deeper water; that is, the tidal current should change first in shallower water. Both of these characteristics were documented previously, with channel currents 1.5-2.0 times as great as those on the flanks and with the latter having a phase lead over the former of about 40 minutes (Weston 1982). O 2.2-2
Salem 316(b) Demsustration Two features of the east shore, Hope Creek Jetty and Sunken Ship Cove, influence the near-field current pattern in the vicinity of Salem (Weston 1982). During early flood tide, the jetty effectively blocks i the flow and deflects the tidal currents in the adjacent region offshore toward the channel. As Hope' Creek Jetty is overtopped during late flooding tide, water appears to exit Sunken Ship Cove and follow the l' Artificial Island shoreline, producing a time-delayed or residual tidal current dominated by the flood. During early flood, deflection around the cove may influence the tidal flow in the vicinity of the Salem station by adding an offshore and upstream component. As the jetty overtops, some water exits Sunken Ship Cove, and a shoreline current
, develops in front of the Salem intakes. During ebb tide, the cove is l l sheltered by Artificial Island and small currents are observed there.
Estuarine residual currents, defined as the net movements of water after tidal influence is discounted, are responsible for the net exchange of water between the estuary and the nearshore ocean. They occur as a result of three known sources: (1) tidal rectification (inertia dif-ferences between the tides), (2) atmospheric forcing (wind and pressure differences),' and (3) gravitationally induced circulation (the density difference between salt and fresh waters) (Pape and Garvine 1982). Drif ter studies conducted by Pape and Garvine indicated that residual
, currents resulting from effects of the classical estuarine circulation
- (two-layer flow) exhibited by the Delawsre estuary are active as far as 40 km offshore of the entrance and, further, that these currents are directly coupled to those of the waters of the adjacent continental shelf. Surf ace flow on the adjacent inner shelf is generally southward at 10 cm/sec, whereas bottom currents tend to converge on the mouth of F
the estuary. Inside Delaware Bay, residual flow moves principally up the main channel and spreads laterally into the adjacent shallower areas on both sides of the Bay. i Net tranports between Delaware Bay and adjacent waters were calculated by Salter (1973). He determined that at the mouth of Delaware Bay there is (1) a net seaward transport on the surface and on the Cape Henlopen side of the Bay during ebb tide and (2) a net upstream transport in the deeper channels and in the bottom water in the Cape May side during flood tide. Total transport was estimated to be 4.323 x 109m3 on the ebb tide and 4.052 x 109m 3 on the flood tide. Total movement of mter between the estuary and coastal shelf on flood or ebb tide is equivalent to about 23-24 percent of the standing volume of the estuary measured at mean tide level. Tidal forces generally determine current speed and direction in' the estuary; the direct effect of river discharge on tidal flow is quite small, particularly in the lower Bay. However, estuarine-circulation type within the Bay has been observed to change when the river flow changes the Bay's salinity structure (Polis and Kupferman 1973). In general, as the discharge increases, the estuarine circulation will change from partially mixed to a stratified or two-layered circula-tion pattern in which the fresh water overrides the sea water forming a " salt-wedge" (Polis and Kupferman 1973). The extent of estuaiine u 2.2-3
Sslem 316(b) Demonstration circulation at any given time in Delaware Bay may be partially deter-mined by examining the salinity patterns. These patterns are described in detail in Section 2.3. 9 O 2.2-4 i --- - . - - . _ . . _
l Sclem 316(b) Demonstratica TABLE 2.2-1 DRAINAGE AREAS AND GAUGED RIVER FLOWS OF STREAMS TRIBUTARY TO DELAWARE RIVER AND BAY (*) Drainane Area Averane Discharge River or Stream las mi a /sec ft /sec m / min /km ft 3/sec/m Delaware at Trenton 17,560 6,780 332.8 11,750 1.14 1.73
, Crosswicks Creek 217 84 3.9 136 1.20 1.82 Neshaminy 544 210 8.2 291 0.83 1.26 Rancocas, North Branch 287 111 4.9 173 0 .96 1.46 Schuylkill at Philadelphia 4,903 1,8 93 83.9 2,96 2 0.95 1.44 Chester Creek 158 61 2.5 87 0.83 1.27 Brandywine Creek 813 314 13.8 486 0.87 1.32 White Clay Creek 228 88 3.4 119 0.91 1.36 Maurice River 293 113 4.8 169 1.02 1.56 1
Total gauged 25,003 9,654 458.2 16,173 1.08 1.64 Ungauged area 11,067. 4,273 202.9 7,17 9(b) 1.08 (1.64) ; l Total drainage 36,070 13,927 661.1 23,352 1.08 (1.64) 2 (a) Drainage areas greater than 130 km2 (50 mi )S 2 l (b) Ungaugedareamujtipliedby1.10=averagem/ min /km (1.68 average ft /sec/mi 2), l Source: Ketchum 1953, with 1980 data updated from USGS 1981a,b. I' l t 9 [ v i l
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i Salem 316(b) Densnstration ! 2.3 WATER OUALITY The physicochemical characteristics of the water influence both the , biological productivity and the distribution of species in the Delaware system. Salinity, temperature, and dissolved oxygen are three param- ! eters that influence the biological productivity and the trophodynamics of the system. 2.3.1 SALINITY Salinity in the Dalaware estuary varies from fresh water (typically , defined as <0.1 ppt) at Trenton to typical ocean water concentrations , of about 32 ppt on the continental shelf off the mouth of Delaware Bay. The amount of salt intrusion from the ocean into the estuary is determined by freshwa'.: discharge, with average longitudinal salinity approximately inversely correlated with mean freshwater discharge. Variables such as tidal phase, basin morphology, and meteorological conditions also affeu salinity. Figure 2.3-1 illustrates the general seasonal patterns tr. the horizontal and vertical distribution of salin-ity in the estuary High freshwater discharge conditions typical of spring runoff normally result in downstream displacement of the salt-front to about rkm 80 and increased vertical salinity stratification. During low freshwater flow conditions in late summer and fall, the salt-front normally extends to about rka 120 and the system is well mixed vertically. The partial stratification evident in the Delaware Bay during periods
-of high freshwater flow results from Se tendency of the fresh water to flow over the denser salt water. The potential energy produced by this density gradient increases convective mixing in the system, and along
- with tidal mixing (Section 2.2), contributes to the transport of water
, and planktonic organisms between the Bay and the continental shelf. In the vicinity of Salem, salinity ranges from about 0.5 to 20.0 ppt, l depending on the magnitude of freshwater input to the system and the I other controlling factors outlined above. The relationship between freshwater flow and salinity near Salem is evident in Figure 2.3-2. Salinity varies inversely with the magnitude of freshwater flow and is greatest during late summer and early fall, and least in late fall and spring. For example, salinity levels at the plant during 1980-1981 were generally higher than those in 1970-1979, corresponding to below-average freshwater flows during 1980-1981 (Figure 2.3-3). There is a marked change in the species of fish and invertebrates
-inhabiting the area in response to salinity variations. For example, when freshwater flows are high and salinity is low, organisms typically l' found in freshwater environments will predominate, and when freshwater
! discharges are low and salinity is high, more brackish and marine forms i will reside. The influence of salinity on the aquatic biology of the system is discussed in Sections 2.5 and 5 of this Demonstration. O 2.3-1
Salem 316(b) Demsnstrctica 2.3.2 TEMPERATURE Just as the salinity of the Delaware estuary is determined by the flow O characteristics of the entire drainage area, temperature patterne in the Delaware estuary are determined by the thermal characteristics of the Delaware River, its tributaries, and the coastal ocean waters. Temperatures of these sources are altered by air temperature, humidity, wind, insolation, cloud cover, and tidal mixing. The temperature of the Delaware River at Trenton, which constitutes the major freshwater input to the estuary, varies annually from 000 l in mid-winter to over 300C in summer (Figure 2.3-4). Periods of rapid temperature change occur in spring and fall. Atlantic Ocean water that , enters the estuary exhibits a less extreme annual range of temperature. I Minimum mean temperatures of approximately 60C usually occur in February ! or March; a maximum of approximately 240C occurs in August (Polis and Kupferman 1973). Thus, the large volume of shelf water that enters the l Bay on each tidal cycle and mixes with the fresher water tends to moder-ate the temperature regime of the lower Bay. The temperature difference in the two major water inputs to the estuary l produces a themal gradient within the Bay (Figure 2.3-5). In winter, l temperature increases from the upstream limit of the estuary near Tren-l ton to the Bay mouth. The gradient can be as large as 4-500. In summer, the direction of the gradient is reversed so that temperature i decreases from Trenton to the Bay mouth. Vertical stratification may occur and produce higher temperatures at the surf ace than at the bottom. h I Thus, maximum temperatures during summer would be likely to occur at the ! surface near the head of the estuary and minimum temperatures near the I mouth at the bottom. During spring and fall, when river and offshore water temperatures are changing most rapidly and freshwater tributary flow and temperature are also quite variable, the temperature gradient within the estuary is less predictable. 1 Data from 1981 sampling demonetrate the nearly isothermal conditions with depth in spring and fall, and the temperature gradient typical of summer conditions (Figure 2.3-6). In late April, semimonthly mean temperature ranged from about 140C above rkm 100 to 12.50C at the Bay mouth. In the Bay proper, surface temperature ranged up to 20C higher at the surf ace than at the bottom. Upstream from rkm 45, however, temperature differences between surf ace and bottom were generally <10C. By early June, the gradient had begun to appear as mean temperatures between rkm 60 and 100 approached 220C, whereas temperatures near the Bay mouth were closer to 200C. A vertical gradient near the mouth was due to colder shelf waters moving in along the bottom while warmer Bay waters flowed outward near the surface. O 2.3-2
Salem 316(b) Dem:nstrction r During late July, mean temperatures above rka 70 reached approximately ! 260C. Downstream from rka 70, temperature declined gradually to about 22.50C at the Bay mouth. As in June, vertical temperature differences were pronounced only in the lower part of the Bay where the surface was , ; about 1.50C warmer than the bottom. By late September, the longitudinal temperature difference was reduced to approximately 20C; mean temperature at rka 120 was about 2100 and at the mouth 190C. Vertical differences, where they existed, were gener-ally loc or less. Temperature patterns in the vicinity of Salem are available from a USGS monitoring station on Reedy Island Jetty, about 5 km upstream from Salem station. From 1970 to 1981, average semimonthly mean temperatures ranged from 20C in early February to 260C in late July and early August (Figure 2.3-7) . Minimum semimonthly means were 0.50C (January 1972, 1976, and 1981); maximum was 290C (August 1980). Maximum daily average temperature over this 11 year period never exceeded 300C. The influence of temperature on the aquatic biology of the system is discussed in Sec-tions 2.5.and 5 of this Demonstration. 2.3.3 DISSOLVED OKYGEN The types and distributions of organisms present in the Delaware estuary are determined, in part, by the concentration of dissolved oxygen in the water. Oxygen decreases in solubility with rising temperature, decreas-ing barometric pressure, and increasing salinity. Dissolved oxygen is consumed as organic matter in the estuary decom-poses. These organics originate from both natural sources (such as detrital material) and artificial ones (such as industrial and munic-ipal wastes). Patterns of dissolved oxygen concentration in the Delaware River show a sag, caused by industrial and domestic wastes, near Philadelphia (rka 151-180) (Figure 2.3-8); hcwever, levels recover 20-40 km down-stream of these inputs. In the Philadelphia area during the summer, dissolved oxygen levels may be low enough to block the migration of several fishes. With this exception, the estuary is well oxygenated throughout the year and the high degree of turbulent mixing in the sys-tem results in nearly homogeneous vertical distributions of dissolved . oxygen in the water eclumn. Concentrations throughout the estuary tend to be lower in summer due to increased temperature, salinity, and oxi-dation rates. The seasonal changes in dissolved oxygen concentrations in the vicinity of Artificial Island are shown in Figure 2.3-9. During the period of record, semimonthly mean dissolved oxygen levels range from 2.6 mg/ liter on July 1-15, 1973, to 13.7 ag/ liter on December 16-31, 1976. Since 1976 at Reedy Island, the semimonthly means have ranged from 5 to 13 mg/ liter. 2.3-3 ,.-w - y u . .e.-- ---,..,y *-,,,vv-,y v.,y---w.,,e m,,...,,3-,., ,-, . , - . - - - ,,,-,,.,,mm,,,,ww-, ,,eam.-,.--ww-- am--- . , . , - . , ,., , -
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the Period 1970-1982 in the Delaware System u Salem 316(b) Demonstration Figure 2.3-2 e r e - r - - - - - _ w _ _ . . ~ _ - , , , , . _ . . . - . . . _ _..m.,_,_,.. , _ . _ _. _ ,_.,_ .,,,,. ., , . . , , ,_,,
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-Salem 316(b) Demonstration 2.4 AOUATIC HABITATS The variety and nature of tbn aquatic habitats in the Delaware system can be attributed to.the climate and the morphology, hydrology, and water chevaistry prevailing in the various portions of the Delaware estuary. The following sections briefly describe the major aquatic habitats and biological communities of the Delaware system, with empha-sis on aquatic life that occurs in waters near the Salem station.
Aquatic habitats are classified customarily by zones. I,ongitudioally , the Delaware system can be thought of as a continuum divided into sev-eral zones: freshwater streams, which, in terms of flow, are dominated by the Delaware and Schuylkill rivers (Section 2.2); the freshwater portion of tne tidal estuary and the C&D Canal; a zone of mixing this i tidal: fresh water with the tidal intrusion of marine water into the Delaware estuary and Bay; and the coastal Atlantic Ocean. The seasonal salinity regime, including the location of the salt front, depends pri-marily on the amount of freshwater discharge into the system at Trenton. Vertically, the estuary can be divided into zones defined by light pene-tration. The, upper, thin euphotic zone (the producing zone) extends to the depth of the compensation light level, i.e., the level at which photosynthesis and respiration rates become equal. This zone goes con-siderably deeper in the relatively clear waters of the ocean and the lower Delaware Bay than in the much more turbid water of the upper Bay, mixing zone, and freshwater tidal zone of the Delaware system (Appendix In the vicinity of Salem, the euphotic zone extends from the water 0 I). surface to a depth of 2.5-109.2 cm, depending on the turbidity of the water. The aphotic zone consists of all water deeper than the euphotic zone. Horizontally, the estuary may be divided into _the intertidal, the lit-toral, the subtidal, and the pelagic zones. The intertidal zone lies between the high and low tide levels and is included in the littoral zone. The littoral zone is a nearshore zone extending from the high tide mark offshore until the depth where light penetration to the bot-tom is no longer sufficient to support growth of rooted aquatic plants (i.e., approximately the same as the lower bound of the euphotic zone). The subtidal zone is that portion of the bottom that extends below the lowest-area exposed by the tide. The open water (beyond the vegetated littoral zone) is referred to as the pelagic zone. When all three dimensions are considered (Figure 2.4-1), it becomes apparent that the various characteristics of each dimension combine to produce'a wide variety of aquatic habitats. That is, coastal systems such as the Delaware contain marshes ranging from nearly pure saltwater, through a mixture of salt and fresh water, to pure fresh water; a pela-gie zone that ranges from ocean marine through brackish water, to fresh water, and from euphotic to aphotic; etc. These gradations of habitat extend from the ocean upstream into each of the freshwater s: reams trib-utary to the tidal portion of the system. o 2.4-1
Szlem 316(b) Demonstration - The Salem station on Artificial Island is located at a oint 80 km inland from the mouth of the Delaware Bay (Figure 2.4-1 in the mix-irg zone of tidal fresh water with marine water. h O O. 2.4-2
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Salem 316(b) Demonstration 2.5 A00ATIC LIFE The entire array of species in the Delaware system could be considered as a single biological co== amity. However, to facilitate study, description, and analyses, the more usual approach employed for envi-
- ronmental assessments-is to divide the total of these species into smaller communities or groups of species that occupy the same habitat and serve similar functions. This Demonstration uses the convention of first partitioning the total array of species into two functional divisions
- the producers (plants) and the consumers (animals). Each division is further compartmentalized into community groups defined by the portion of habitat each group occupies. The producers are divided into the vascular plant community (which grow mostly rooted to the bot-tom in shallow water nearshore) and the phytoplankton (very small plants
. that live suspended in the open water column).
The consumers are divided into several groups, including microbes which occupy virtually all habitats in the system; zooplankton, which are small invertebrates, and other animals found in the water column; I benthic invertebrates which are found in and on the bottom; and fish, another group like microbes in that there are different assemblages of fish species found in virtually all habitats in the system, e.g., tidal creeks, marsh lands, bottom dwelling, and open water (pelagic). In this context, the word "found" is used advisedly, because many species are habitat sharers. For, such species, individual organisms are considered to be a part of each of the communities in whatever habitat they are found to occur. For example, those captured in plankton nets are num-O'- bered among the plankton community, whereas other individuals of the same species taken in bottom samples are included as part of the benthic
~
community. Accurate estimation of total population numbers for such species requires summing up of the numbers found in all habitats in the system. i This section of the Salem 316(b) Demonstration describes the biological communities in the Delaware system, with particular emphasis on those
- inhabiting the study area (rkm 0 to 190).
2.5.1 PRODUCERS Producers are plants that use the energy in sunlight to produce organic matter from carbon and other minerals. All animal life is directly or indirectly dependent on this production. 2.5.1.1 Vascular Plants Yascular plants inhabit the littoral zone of the Delaware estuary, mostly in the tidal marshes. They contribute much of the organic matter, primarily in the form of detritus, to the food base for ani-mal life;- provide habitat for a variety of fishes, invertebrates, birds, and ma==als; provide substrate for growth of attached algae; add dissolved oxygen to the waterbody during the highly productive spring and summer months; and act as a biological filter, removing
- ()
carbon monoxide from the air and a variety of pc11utants from the water. 2.5-1
Salee 316(b) Dem2nstrction Approximately 165,000 acres of tidal marshes border the tidal Delaware River and Bay. Most of these wetlands occur in Delaware and the lower New Jersey counties of Salem, Cumberland, and Cape May. Relatively h little wetland occurs in Pennsylvania or in the upper New Jersey coun-ties of Gloucester, Camden, and Burlington (Ferrigno et al. 1973; Daiber et al.1976) . The major chemical and physical factors influencing the. distribution of tidal marsh vegetation in the Delaware estuary are tidal flooding and salinity. Tides have varying effects on a tidal marsh system according to their intensity, vertical inundation, range, and rhythm. Probably the most important influence on tidal marsh vegetation is the distribution and penetration into the tidal marsh system of the salt contained in sea water. Most areas in tidal marshes are exposed to waters of varying salinities periodically throughout the day. Depending on how far up or down bay a particular marsh is located, or how far away from a freshwater stream channel, the degree of saline fluctuation can vary greatly. Thus, chan;;es in salinity are reflected in changes that occur in the nature of the marsh vegetative community as one proceeds both laterally across the marsh surfaces away from the stream channels and up the course of the stream system. Throughout the upper part of the Delaware estuary, extending from Trenton to the Wilmington area, tidal marshes are of the freshwater type. The more common species along this reach are icircus americanu_s, S_. olnevi, Polygonum punctatum, Eleocharis spp., Sagittaria spp., Zizania acuatica, Peltandra virginica, Nuphar advena, Pontederia spp., g and Lythrum spp. (Walton and Patrick 1973). The~se species also occur in inland freshwater tidal marshes along the Bay (Walton and Patrick 1973; Daiber et al. 1976). In general, these species are not tolerant of salinities in excess of 5 ppt. Proceeding southward down the estuary from Wilmington, the carshes grad-l ually change to the saltmarsh type. The more common species along this reach are Spartina alterniflora, S. patens, Distichlis spicata, Iva frutencens, Baccharis halimifolia, and Phragmites communis (Walton and Patrick 1973). These species are euryhaline and, with the exception of P. communis, are tolerant of salinities up to and exceeding sea water. l 2.5.1.2 Phytoplankton l Phytoplankton are minute plants which remain suspended in open water ! and are transported from place to place by water currents. Relative to detritus and other sources of organic matter, the contribution of phytoplankton to the food base is small in the very turbid freshwater and brackish portion of the Delaware system where Salem is located. l The relative contributian by phytoplankton gradually increases in ! the less turbid lower reaches of the Delaware estuary. Under light, temperaturo, and nutrient conditions most conducive to growth and reproduction, phytoplankton produce from one to three cell divisions (generations) per day. Phytoplankton may not grow and multiply at all if any of these requirements are severely limited. h l l 2.5-2
Salen 316(b) Dem:nstration The phytoplankton'in the vicinity of Salem is composed of a mixture of marine, estuarine, and freshwater species typical of Middle Atlantic
- ( } estuaries. During the period 1973-1976, a total of over 101 genera, probably involving several hundred species, were identified in over 300 samples taken on a transect immediately west of Salem. Diatoms dominate (85-93 percent of total abundance), particularly Skeletonema costatum, Melosirs spp., and Nitzschia spp. Abundance is relatively low (mean abundance 772-2,033 cells /al) during winter and highest (7,093-14,493
- cells /ml) in the spring and summer months (PSE&G 1980).
2 Obligate freshwater and marine species with a narrow range of salinity l tolerance (stenohaline) that are transported by currents into this transitional zone with its highly variable salinity succumb to osmotic seress and contribute to the detritus food base. Species able to toler-ate a broader range of salinity (euryhaline) survive, but production is limited by the very turbid water to a depth of about 1 m; this restricts the penetration of' light required for plant growth (PSE&G f 1980). 2.5.2 CONSUMERS
- All aquatic life other than plants are consumers. Consumers are totally dependent, directly or indirectly, for their food and nutrition, on organic matter prodaced by plants. This section describes the mejor
' assemblages or communities of consumers in the Delaware system, with particular emphasis on those in the immediate vicinity of Salem.
2.5.2.1 Microbes Microbes that feed on detritus are the major source of energy used by primary consumers, particularly suspension-feeding and deposit-feeding i ' animals. Sources of detritus in the Delaware system include upland vegetation, vascular plants in the marshlands, macroalgae and phyto-plankton, dead aquatic animals, and wastewater and municipal sewage discharge. The microbes that feed on this detritus, including bacteria, fungi, and protozoa, thus link primary producers to the upper trophic levels (consumers) and constitute an important part of the food web. The detritus-microbe assemblage exists both as fine particles suspended in the pelagic zone, in which case they are considered part of the plankton, and in thick deposits in the marshes and bottom muds of- the Delaware system, in which case they are considered part of the micro- ! . benthos. The microbes decompose detritus, releasing proteins, oils, and other organic compounds that are used by other organisms. They also release many nutrients including various forms of nitrogen, phosphorous, metals, and carbon dioxide used by plants to synthesize new organic - matter. The microbes themselves are probably the primary energy source
- for-aany. detritus-feeding organisms (Odum 1971).
2.5.2.2 Zooolankton i-Zooplankton are small animals that, during most of their existence, ' remain ~ suspended or swim freely in open water and are transported about primarily by currents. They range in size from minute individuals that are too small to collect with standard plankton nets (nanoplankton), to 2.5-3
..+n n-.-, ,m --,,-~,,.-m. w ,,--,.v.y_.-- --g ,.ywn-. mr. m ,m,m,,,e7,, , , ., .,m.p. --ev.,
, -y,m-pm.,,,y, -,,,a q-w g:,,-.-mp,-.---w-
Salem 316(b) Demonstration organisms large enough to be retained in standard 0.07 to 0.08-mm mesh nets (microzooplankton), to larger forms retained by 0.5 to 1.0-mm mesh (macrozooplankton). h The minute (nanoplankton) species such as single-celled protozoa are very limited swimmers, so they are transported about by currents. Growth and reproduction are controlled largely by food supply and water temperature. The microzooplankton retained by fine-mesh (0.08-mm) nets include primarily rotifers, copepods, cladocera, polychaete worms, and a few miscellaneous groups. During seasons of high freshwater runoff (late winter and spring), fresheater forms predominate, such as rotifers spp., Brachionus angularis, and Notholca sp., and the cyclopoid copepod Halicyclops fosteri. During late summer and fall, with low freshwater flow and attendant greater saltwater intrusion, more saline forms such as cteno-phores and the copepods Acartia tonsa and Pseudodiantomus coronatus ' predominate. During spring and summer, growth and overall numerical abundance increases, reflecting reproductive activity and increased larval density. During the period 1973-1976, qusntitative microzooplankton studies were conducted biweekly to monthly among 22 sampling stations in the vicinity of Salem (PSE&G 1980). Monthly station-specific time-duration studies provided data on the vertical (surf ace, middepth, and bottom) distri-bution of microzooplankton at three stations (located on a transect opposite Appoquinimink River) during four consecutive tidal stages over a 12-hour period. A total of 110 microzooplankton taxa were identified h in 2,332 collections taken from January 1973 through December 1976. Larger macrozooplankton (retained by an 0.5-mm net) include organisms that spend part or all of their time in the water column (pelagic zone) and typically include invertebrates, as well as the eggs and larvae of some fish species (ichthyoplankton). A portion of the invertebrates may spend time on the bottom as part of the benthos. Macrozooplankton with sufficient swimming power to exercise some control over th sir location in the water column are included in the nekton. Most species migrate vertically each day to arrive at preferred levels of light intensity an % - *ood supply. Some groups, such as mysids and amphipods, are most abunactt near or on the bottom, but also migrate vertically in the water column, particulcrly during nighttime hours. Macrozooplankton that migrate vertically can presumably take some advantage of two-layer circulation patterns in estuaries to stay within a tolerable range of salinity; those that drif t beyond their range of salinity tolerance succumb and are eaten directly or contribute to the detritus food base of estuarine systems. A total of 46 taxa were identified from 492 samples, but only two taxa, Gammarus spp. and Neomysis americana, together typically comprised at least 80 and, occasionally, as much as 95 percent of the total abun-dance. Changes in the composition and numerical abundance of macrozoo-plankton reflect seasonal variation in factors such as freshwater flow, salinity, and temperature, and within a more reduced time frame, tidal h currents, light intensity, and predation. 2.5-4
Salem 316(b) Descastration a The distribution of larval stages of some species whose adults live in
/^% - or on specific substrates reflecte the-location of these parent adults. -- Examples include the grass shrimp (Palaemonetes purio), the fiddler crab (Uca BiBAE), and the mud crab (RhithroDanoDeus harrisii). Larval and juvenile grass shrimp were collected in greatest density in inshore areas, fiddler crabs were most abundant near intertidal mud banks and at the mouths of tidal creeks, and mud crabs were found primarily near oyster-shell beds such as those off Mad Horse Creek. Tidal dispersion quickly distributes these forms throughout the lay and lower River.
Biotic f actors such as predation, competition, and parasitism may be significant in controlling zooplankton abundance. Predation is probably most significant. A predator-prey relationship is suggested by the lagged response between microzooplankton and macroinvertebrate abun-dance. This relationship is especially evident .from late spring through summer. During late summer /early fall, the etenophores and hydromedusae prey extensively on microzooplankton. This phenomenon has been evi-denced by Miller (1970) who estimated that mophores may reduce the standing crop of microzooplankton by 25 pet, per day. 2.5.2.3 Benthic Invertebrates The benthic invertebrates (benthos) include all iuvertebrates living within the bottom sediments (infauna), on the surf ace of the bottom
- sediments (epibenthos), and on other solid substrates such as rooted aquatic plants, bulkheads, pilings, and breakwaters. A total of 57
(~} taxa representing 8 phyla was identified from the 1,044 Ponar grab V samples taken. The benthic invertebrate community near Artificial Island consists primarily of resident euryhaline forms tolerant of the wide range of conditions occurring in this reach of the estuary. The attached benthos (e.g., hydroids, oysters, and barnacles) are important as habitat formers (i.e., shelter and attachment surfaces) for other invertebrates. The principal factors regulating community composition, distribution, i and abundance are salinity, temperature, and substrate. Of these, the . availability of suitable substrate is the predominant factor governing distribution and abundance of many taxa in this reach of the estuary. These factors combine to produce communities characterized by rela-tively low diversity with a few numerically dominant taxa including Scolecolioides viridis,'Polydora sp., Paranais litorclis, Balanus imorovisus, and Cyathura colita. Each substrate type has its characteristic assemblage of organisms due to the various species habitat preferences and/or dependencies. Substrate type in turn is primarily determined by water velocity, , since velocity af fects deposition of sediments. Near Artificial Island the basic substrate types are sand, clay, mud, and to a lesser extent gravel-shell. Sand substrate has low organic content, is subject to scouring by
< O' strong currents, and lacks attachment surfaces. Species richness 4
(7-10 annually), density, and biomass were least in this substrate. 2.5-5 4
.-,,,e~, - n n. -,. --, - - - , _ , , - - ~ - - , , , , , - - - - . - , - ~ , . - - - , , , - , - , , , - - - - -n ~,-,n,,- ,,,,ne-~--v--,,,. ,
,,.,,,--,,an----.-~e
Salem 316(b) Demonstrction Sand substrate has limited ability to support infeuna or epifauna, as reflected by the fact that S. viridis, although dominant in sand (Figure 2.5-1), was much more abundant in other types of substrate. h Clay substrate also is characterized by low organic content, high sus-ceptibility to scouring, and little attachment surface. It consists mostly of clay, silt, and some detritus. Species richness (9-12), density, and biomass were moderate. Polydora sp. was the dominant taxon in clay and was less common elsewhere (Figure 2.5-1). Mud has high crganic content, little attachment surf ace, and is typical of depositional areas with slow current velocities. Species richness (12-13), density, and biomass were moderate. Paranais litoralis was the dominant taxon in mud (Figure 2.5-1). Gravel-shell substrate has high organic content and a wide range of attachment surf aces including small rocks, gravel, and shell. It pro-vides food and habitat for many benthic organisms. Species richness (16-19), density, and biomass were greatest in these areas. Balanus improvisus, which requires firm substrate for attachment, was the Zominant taxon (Figure 2.5-1) . Taxa using this substrate for surface attachment include the mussel (Genkensia dimissus); the oyster Cras-sostrea virrinica; the anemone Diadumene leucolena; and some ectoprocts (bryozoans). The nudibranch Doridella obscura, which feeds on ecto-prouts, was taken only on gravel-shell. Seasonal changes in salinity and temperature af feet the local community structure. Salinity is probably the more important factor. When g salinity is high, in summer and fall, there is greater diversity near Artificial Island due to species movement (such as the isopod Edotes triloba and the cumacean shrimp Leucon americanus) into the study area from downbay. Larval stages of several species migrate into the area in summer and fall, and temporarily become established in low density ! in the benthos, e.g., the polychaetes Giveera dibranchiata, Giveinde solitaria, and Sabe11 aria vulgaris; the pelecypods Mulinia lateralis and Mya arenaria; and the tunicate Molgula manhattensis. Water temperature controls reproductive activity for many species and is associated closely with seasonal increases in benthic populations. This is best evidenced by the occurrence of recently set larvae of B. improvisus shortly af ter optimum temperature for reproduction. The epibenthic portion of motile populations such as N. americana, Gammarus spp., and blue crab (Callinectes sapidus) are not efficiently sampled by grab samplers. Blue crab appeared in bottom trawls through-out the study. Also, although Gammarus spp., N_. americana, and many other invertebrate taxa are expected to live among the aquatic vascular plants in the extensive wetlands of the Delaware system littoral zone, they cannot be sampled there by conventional methods. Annual mean abun-dance of the benthic invertebrates in the Ponar grab samples ranged from 17,000/m2 in 1976 to 25,000/m2 in 1974 (PSE&G 1980). The results of these studies, from 1968 through 1976, are summarized here and detailed in PSE&G 1980. More extensive discussions of Gammarus spp and N. 2.5-6
Salem 316(b) Demonstration americans are contained in Section 4 and Appendixes II and IV of this
-Demonstration.
The blue c.rab, an annual resident of the Delaware estuary, migrates extensively in the system and uses a wide variety of habitats during its 2- to 3-year life span. It ranges from tidal fresh water near Burlington, New Jersey (rkm 189; rm 117) (Lynch 1979), to as far as 32 km (20 mi) off the Bay mouth in full sea water (Epifanio 1979). From Marcus Hook, Pennsylvania (rka 128; rm 80), south to the Bay mouth, blue crab are seasonally abundant and support one of the drainage's most important commercial fisheries (Section 2.6.2) in the drainage area.
.Near Artificial Island, blue crab are rarely collected in January and February; the first captures typically cccur in mid-March in the south-era portion of the study area (Figure 2.5-2). As temperature increases, crabs become more numerous and migrate progressively northward. By May, crabs are common and well distributed throughout the area, and usually in June the first of two abtudance peaks occurs. Crab abundance declines in' July and August, primarily due to natural and commercial fishery-induced mortality and continued upstream migration out of the l area. By mid-August, the new year-class begins to move into the area.
Essentially, all have completed their larval development and are juve-niles, although a few megalops are taken (PSE&G 1980). The influx of these young crabs results in the second abundance peak in September and < October. 2,5.2.4 Fis). Fish are the principal upper-level consumers in the Delaware River estusry - ocean system. Studies of the fishes in the Delaware estuary l and associated tidal creeks have been conducted for PSE&G by Ichthyo-i logical Associates, Inc. (IA) from 1968 through 1982. Similar to the other aquatic communities described previously, the fishes in the vicinity of Artificial Island include freshwater, marine, euryhaline-estuarine, and diadromous species. Over 90 species of fish were col-l 1ected from January 1970 through December 1976 during the preoperational studies (Table 2.5-1). Of these, only nine species were present in j all life stages from egg to adult. These were the blueback herring, elevife, bay anchovy, tidewater silverside, Atlantic silverside, white perch, striped bass, weakfish, and hogchoker. Relative and absolute l cbundanca varied, reflecting variations in year-class production, changes in distribution patterns, availability of food organisms, etc. (PSE&G 1980). The various fish species near Artificial Island can be divided on the basis of life strategy into two distinct groups of resident and migra-tory forms. Residents can be classified further by salinity preference as either tidal-freshwater or estuarine residents. By the nature of their movements, migratory groups can be divided among waters of dif-fering salinity into three groups: diadromous species, predominantly estuarine types, and predominantly marine types. The predominantly estuarine types include hogchoker, white perch, bay anchovy, Atlantic and t'.dewater silversides, naked goby, and mummichog. Predominantly marine species that use the estuary are the weakfish, spot, Atlantic 2.5-7
Salem 316(b) Dem:nstration croaker, and Atlantic menhaden. The notable diadromous migratory species are American eel, blueback herring, American shad, striped bass, and alewife. h Large seasonal variation in physicochemical conditions, most notably water temperature and salinity, as well as in the productivity of lower trophic levels, results in large variation in composition, abundance, and distribution of the region's ichthyofauna. Within the community, mechanisms have evolved that allow the efficient, and obviously sequen-tial, use of available habitats and resources. Examples are the differ-ences in the timing and location of spawning among the species and the resulting recruitment, and the habitat selection and feeding behavior of all stages. Within each season, but perhaps to a lesser extent in winter, constant patterns of immigration and emigration are apparent, all keyed to opti-mal use of available resources. This cycle of community transition is the key to an overall stability and harmony that is reflected in annual patterns. During spring and fall, najor changes in water temperature and salinity prompt shifts in community composition as species adjust their distributions to seek preferred reproductive, nursery, or over-wintering conditions. As temperature and salinity become more stable, so does the community, with many species using the warm, highly produc-l tive summer period for reproduction and growth; only a few reside in this area during the cold period. In spring, species variety increases with water temperature; estuarine residents move from downbay overwintering areas, anadromous species move h from offshore waters through this region to freshwater spawning grounds, l and progeny of several estuarine-dependent marine fish migrate or are transported to low-salinity nursery areas. Adult bay anchovy, Atlantic silverside, hogchoker, and white perch typically arrive near Artificial Island from downbay in March and April to feed in preparation for later spawning. Mummichog, among the few fish to overwinter in tidal creeks and tributaries, become active in the shore zone as they, too, prepare for spawning. The anadromous striped bass, American shad, blueback herring, and alewif e pass through the study area en route to spawning grounds upstream and/or in tributaries. During May, as adult bay anchovy and hogchoker reach spawning condition, they begin to move back downbay to higher salinity spawning grounds. This movement continues through summer as younger specimens progres-sively mature. Adult weakfish (which have entered the Bay from off-shore) and adult naked goby also begin to spawn downbay. By mid-June, progeny of all these species typically have moved into low-salinity nursery grounds. Their abundance increases and remains high through summer when saline conditions are favorable. Young spot and Atlantic menhaden prefer even less saline water, and follow the upstream move- , ment of the oligohaline portion of the nursery. During July through ! September, spawning activity slows and young of the summer community dominant species reach peaks in annual abundance. O 2.5-8
Sclem 316(b) Demonstration Abundance declines during late September, October, and November as decreasing water temperature and productivity initiate emigration to overwintering areas downbay and/or offshore. Lowering water temperature also prompts the gradual movement of spot, Atlantic menhaden, and the herrings through the Artificial Island area from ' upriver utirsery grounds to downbay or oceanic overwintering areas. In response to lowering j salinity and temperature, white perch also move into the area from upriver in fall. Conversely, progeny of the ocean-spawning, but estuarine-dependent Atlantic croaker migrate into the area during f all and use it as a nursery until minimum water temperature (in January or February) prompts their return downbay to warmer water. During winter, variety within the local ichthyofaunal community is low and only white perch, hogchoker, and . silvery minnow are common. Low water temperature limits activity as metabolism slows ad generally restricts the distri-bution of these fish to the deeper waters. Just as patterns of immigration and emigration distribute resources temporally for species that occupy similar niches, species that occur simultaneously share resources through differing habitat and food pref-erences. During spring and summer, for example, the community consists of demersal species (i.e., spot, hogchoker, and weakfish), shorezone inhabitants-(i.e., Atlantic silverside and mummichog), and open-water pelagic forms (i.e., Atlantic menhaden and bay anchovy). Within general habitat types, further allocation of. reso trees is accomplished through even more subtle preferences. For example, both Atlantic silverside and mummichog occur within the shorezone habitat, but exhibit preferences to sand and mud substrates, respectively. Even among species with similar habitat preferences, feeding selectivity reduces competition for avail-able food. For example, although spot and hogchoker are both bott<m 4 feeders, spot feed principally on epif aunal crustaceans, wheren hog-choker feed primarily on infaunal annelids. Bay anchovy and Atlantic menhaden are both pelagic -planktivores; however, the difference in coin-cident life stages may limit direct competition for food organisms. 2.5.3 ENDANGERED, THREATENED, OR SPECIAL-STATUS SPECIES l The shortnose sturgeon (Acipenser brevirostrum) is the only fish species in the Federal Register list of threatened or endangered species that i is known to occur in the Delaware estuary. No shortnose sturgeon were collected in field samples from January 1970 to 1977. Only five speci-mens were collected at Salem in station and field samples from 1978 through 1982. All live specimens were returned to the River. Several species of sea turtles occur _in the Delaware estuary during the warmer summer months when the adults migrate northward for feeding. These species include Atlantic loggerhead (Caretta caretta), Kemp's
- Atlantic Ridley (Lepidochelys kempii), and Atlantic green (Chelonia sydse E ds a.g). Ten sea turtles were found on Salem's trash bars through July 1983; eight were . dead. All turtles were reported to the Marine Mammal Stranding Center. Four additional sea turtles were taken in field samples. All were alive and released unharmed. No sea turtles lI were taken prior to July 1979.
2.5-9
,r m p p-TABLE 2.5-1 FISHES COLLECTED FROM THE DELAWARE RIVER AND TIDAL TRIBUTARIES NEAR ARTIFICIAL ISLAND ANNUALLY DURING JANUARY 1970 THROUGH DECEMBER 1976
! 1970 1971 1972 1973 1974 1975 1976 Life g,) Typeng Rany Rank Peak Rank Rank Rank Rank Snecige Staae Cear Occur T:S Occur 1 1 Occur T:S Occur T:S Occur T:S . psigI T1!_ 9gsyt T:S Sea lamprey Y,A P,T C + + + + + + Cowncoe ray A T + Atlantic sturgeon Y 7,C + + + + + American eel Y,A P S.T + 7; + 10; + 7; + 7; + + 10;10 + Conger eel Y S + Blueback herring E,L,Y,A P S.T.C + 6;3 + 8;5 + 9; + 10;4 + 7;8 + 8; + 8;10 Hickory shed Y,A S.T.C + + + + + + Alewife E.L,Y,A P,S.T.C + 5;8 + 743 + ;4 + + + + 10; cn American shed Y,A S.T.C + + + + + + + b Atlantic menhaden L,Y,A P.S.T.C + ;5 + 6;2 + 6;3 + 6;7 + 5;3 + 7;3 + 7;3 Atlantic herring Y,A T,C + + + + + u i Cizzard shed Striped anchovy L,Y,A Y,A P.S.T.C S.T
+ +
+
+
+
+
+
+
+
+ +
+
g n Bay anchovy E.L*,Y , A P.S.T.C + 1;2 + 1;4 + 1;2 + 1;2 + 1;l + 1;2 + 1;I U ,' Eastern mudainnow A S + + t3 Redfin pickerel Y,A S + + + + g i Chain pickerel Y,A S + + + o ! Inehore lizardfish Y,A S,7 + + + D Coldfish Y,A S,7 + + + + + + ct 4 Carp Y,A S.T C + + + + + + + y rt
- Silvery minnow Y,A P.S.T + + + 37 + ;6 + 10; + + 9; g*
, Colden shiner Y,A ST + + + + + .
+ p Satinfin shiner Y,A S,7 + + + + + '+ +
Spottall shiner Y,A S,7 + + + + + + + 1 Creek chub A S + White sucker A S + + + Creek chubsucker Y S + + White catfish Y,A S.T.C + + + + C + + Brown bullhead L,Y,A P.S.T.C + 10; + + 10; + + ,
+
- Channel catfish Y,A S.T.C + + + + + + +
1 4 (a) E = egg , L = La rve , Y = young , A = adul t . , I (b) P = plankton net, S = seine, T = trawl, G = gill net. (c) Top 10 species in river samples are ranked. 1 i I 4
(() C) U TABLE 2.5-1 (pane 2 of 3) 1970 1971 1972 1973 _j 974 1975 1976 Rank Life (,) Typesgg Ran ,) Rank Rank Rank Rank Rank Species $13ae fear Occur 11 9sstL IIS. Occur T.S Occur Tis _ Occur I;1_ Occur Iis._ occur 7:S Oyster toadfish L,Y,A P,T + + + + + + + Silver hake Y T + + + Red bake Y T + + +- + + Spotted bake Y T + + + + + + 9; + Striped cusk-eel Y,A P.T + + + + 9; + + Halfbeak Y S + + Atlantic needlefish Y,A S,7 + + + + + _+ + Sheepshead minnow Y,A S + + + + + + + Banded killifish , L,Y,A P,S,7 + + + + + + + Hummichog L,Y,A P,5,T + 4; + ;7 + ;5 + ;5 + ;6 + 35 + ;5 m H Striped killifish Y,A S,7 + + + + + + Rainwater killifish Y,A S l
' Hosquitofish A S + + g Rough silverside Y,A P.S.T + 39 + + + ;10 + 310. + ;8 ;6 e-.
Tidewater silverside E.L,Y,A P.S.T + 310 + + + 38 + ;4 + ;4 ;8 % tt Atlantic allverside E.L,Y,A P,S,7 + gl + 31 + 31 + 31 + 32 + gl + ;2
- Fourspine c
- stickleback A S + + g l Threespint o stickleback + + + + + IS L,Y,A P.S.T +
Lined seshorse A T + $ Northern pipefish L,Y,A P,S,7 + + + + + + + H ] m a et White perch E.L,Y,A P.S.T.C + 3;7 + 2;9 + 2;6 + 3; + 4;9 + 6; + 4;9 F-Striped base E.L,Y,A P.S.T.C + 8;6 + 9;8 + 8;9 + 8; + + + $ Black sea bass Y T + + + Bluespotted sunfish Y,A S + + Pumpkinseed L,Y,A S,T + + + + + + + Bluegill L,Y,A S,7 + + + + + + + Smallmouth bass Y S + Largemouth bass Y,A 8 + + + + + + + White crappie Y,A S,T + + + + + + + Black crappie Y,A S,T + + + + + + + Tessellated darter Y,A S,T + + + + + + + , Yellow perch L,Y,A P . S .T .'; + + + + + + +- Bluefish Y,A P.S.T.C + 9; + ;10 + ;10 + ;9 + ;7 + ;7 + ;7
+ + +
Crevalle jack Y P.S.T + + + + Lookdown Y T + +
p) N,_
/m .
b 3 TABLE 2.5-1 (pane 3 of 3) -
- r. .
12Z0 1971 1972 1973 1974 1975 1976 Bank Rank Rank Rank Life g,) Typeng Bang,) Rank Rank Species Staae gg.a r occur T.5 Occur T:S Occur T:S Occur 11E_ Occur Ilf. 9ccur T : 8 .. Occur 7;S .. Pinflah Y S +
+ + + + + + +
Silver Perch L,Y,A P S.T Weakfloh E.L,Y,A P,8,T.C + 2; + 3; + 4; + 4; + 6; + 3; + 6; Spot L,Y,A P,5,T C + + 5;4 + 3;8 + 2;3 + 2;5 + 4;6 + 3;4 Northern kingfish Y T + Atlantic croaker L,Y,A S.T + + + + 9; + 8; + 2; + 2;
+ + + + + +
j Black drue L,Y P.S.T Spotfin butterflyfish Y T + y Striped mullet Y S + + + w White mullet Y S + + g Northern stargazer Y T + + + + + y ~ Sand lances L P + e Naked goby Seaboard goby A L,Y,a P.S.T T
+ + +
+
+ + + +
Q v Atlantic mackerel A T + n Spanish mackerel A C + Butterfloh Y,A P,T,C + + + + + + p , Southern searobin Y.O T + +
+
+ $
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Salen 316(b) Demsustration 2.6 COMMUNITY ECOLOGY a.g 2.6.1 ENERGY FLOW AND TROPH0 DYNAMICS Temperate estuaries, such as the Delaware, ' Hudson, and Chesapeake rank among the most productive of environments; they damonstrate unique char-acteristics that render them more than mere pathways between fresh and marine waters. Although considered a highly stressful habitat in a ' physiological sense, due to widely varying physical and chemical condi-tions, estuarine' biological communities demonstrate a seasonal suc-cession of plants and animals that results in a maximized productivity in this rich environment. Energy needed to drive this production is derived originally from sunlight; however, growth within the estuary is determined by interactions among the estuary's biological components, interactions with adjacent systems, and the effects of the physical characteristics of the estuary itself. Energy imports must be balanced by exports in any biological system, and this is equally true of the Delaware. However, total production within the estuary, at times, can be substantially greater than instantaneous input due to the large degree of recycling that occurs within the estu-ary, primarily in the form of living organisms and detritus. Energy input into the Delaware estuary occurs through a number of path-ways. The ultimate source of energy--sunlight--falls directly upon the estuary itself and is converted and stored through photosynthesis by microscopic plants in the water column (phytoplankton), by larger algal forms, or by ' the vascular plants of the fresh and brackish water marshes. In estuaries with extensively developed marsh syste:n like the Delaware, primary production of tidal marsh plants typically exceeds primary production from other sources. In recent studies on the Dela-ware, it has been shown that the phytoplankton production may equal the tidal marsh production (Pennock et al. 1983). Phytoplankton energy
. inputs are typically small in the turbid upper estuary and increase dramatically in the relatively clear waters near the mouth, whereas total production due to larger sigal forms is generally considered small l
throughout the estuary. A second source of energy in the estuary is naturally occurring dis-solved organics, detritus, and live organisms entering f rom the various tributaries and the ocean, and sources of point and nonpoint organic material and nutrients. Examples of the former type of input include , leaf litter washed into the estuary from the drainage basin; micro- and macro-invertebrate animal assemblages (zooplankton and benthos) that are transported into the estuary on the tides; and the various marine and i anadromous fish that use the estuary as a spawning and nursery ground. Due to the relatively low productivity of the marine environment, bio-logical energy inputs from the ocean generally are considered small. Examples of the latter type of input include agricultural runoff and wastewater from sewage treatment plants. These energy inputs are dis-cussed in detail in the next section. ' In highly developed and indus- , trialized areas such as the upper Delaware estuary, anthropogenic point
'- and nonpoint sources of heat, organic matter, and nutrients can some-times far exceed natural sources of stored energy.
2.6-1
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Sclem 316(b) Demonstrction Energy can leave the estuary in different forms. First, there are the products of normal respiration, including heat, as well as various excretory and fecal products. These products, along with various decom-h position products, including dead and dying organisms, detritus, and dissolved organics, may be removed from the estuary passively by tidal exchange with coastal waters. Further, the energy associated with living biomass may be lost when organisms such as phytcplankton are passively transported out of the estuary by tidal currents or when organisms actively emigrate from the system. Between the times of input into and export from the estuary, energy can be used and transfonned many times while passing through the varicus trophic levels. Stored energy at any particular trophic level is either consumed by the next trophic level, recycled through the detritue psol, or removed from the system. The detritus pool is a major M.a for energy and nutrients in the estuary; it buffers the wide fluct.ntion in energy inputs, permitting increased system ef ficiency. Energy (rom this pool is made available to other trophic levels by bacterial and fungal decomposition, consumption by detrivores, or through direct leeching of the organic material into the water column. The diverse vommunity of benthic and epibenthic detrivores provides the major route for recycling available energy from detritus to higher trophic levels. The general energy flow diagram (Figure 2.6-1) describes the system from a functional point of view, but the actual ecosystem oehavior is much more complex. As their environment is highly variable, many estuarine organisms are omnivorous, or at least able to change diet with age. This feeding behavior permits them to use various available food sources g and thus increases their likelihood for survival. In light of these adaptive mechanisms, the actual food web describing energy and nutrient transfer among various species groups within the Delaware is exceedingly complex; however, a basic descriptive food web applicable to the Dela-ware estuary is offered for greater perspective. Figure 2.6-1 depicts the location of zcoplankton near the bottom of the food web. As described in Section 2.5.2.2, they range in size from the minute nanoplankton to macrozooplankton. Tne minute zooplankton feed on detritus and the smallest of phytoplankton cells. They, in turn, are eaten primarily by larger zooplankton and by filter-feeding benthic invertebrates and fish, as well as larvae of fish and invertebrates. Microzooplankton feed on detritus, phytoplankton, and nanoplankton and, in turn, are eaten by larger invertebrates and fish. The macrozooplank-con follow a similar pattern; however, in addition to their consumption of phytoplankton and detritus, some species are omnivorous, feeding on smaller invertebrates, fish eggs, and larvae (including their own species). Higher in the food chain are benthic and epibenthic invertebrates, which include such species as Neomysis, Gammarus, and blue crab (Callinectus s ap idus) . Both larvae and adults are essential components of the estu-arine food web as prey for higher level consumers such as fishes. Most organisms among these invertebrates are primary consumers that feed on h phytoplankton and detritus, yet many species can operate at different 2.6-2
Salem 316(b) Descastration
.. trophic levels simultaneously. For example, Neomysis is a grazer, feed-ing on zooplankton and larval fishes when available. As noted earlier,
, . - ' their ability to easily switch from one food source to another permits
.Neomysis to avoid the effects of wide fluctuations in the abundance of any individual prey.
Blue crab, on the other hand, is an example of an organism whose diet Larvae are dependent on plankton, but with increasing i varies with age. size they feed on progressively larger items. The juveni.les and adults frequently feed on salt marsh grasses (Spartina spp.) in addition to other aquatic vegetation (Truitt 1939). The species is considered an important estuarine scavenger, but also is an active swimmer and able to capture live fish (Barnes 1968). The alteration of feeding behavior, whether according to life stage or across all life stages, prevents the formation of tight linkages 4 (predator-prey) between various species. This flexibility means that , changes in the abundance of one . species may not have a direct influence on the abundance of other species within the estuary. The evolution of the biological communities in estuaries such as the Delaware estuary has resulted in a maximized productivity in this highly
. variable and naturally stressful environment through adaptive feeding behaviors that tend to buffer the effects of environmental fluctuations.
2.6.2 HUMAN USE OF THE DELAWARE SYSTEM 4 Use of the Delaware River and Bay by the human population generally i can be divided into four overlapping categories: (1) recreation; (2) commercial, industrial, or municipal uses; (3) transportation; and (4) water supply. Recreational uses include fishing, crabbing, , and boating. ~ Commercially, the Delaware estuary supports active finfish and shellfish fisheries. Industries and municipalities use the Delaware system both for water supply and disposal of treated wastewater and stormwater runoff. Transportation uses of the River and Bay mainly involve the shipment of freight to and from such major ports as Phila-delphia and Wilmington. The Delaware system also is used as a water supply for municipal, industrial, and institutional needs. 2.6.2.1 Recreational Uses l National surveys indicate a nearly threefold increase -in marine angling i from 1955 to 1985 (Stroud 1977) and surveys in the State of Delaware indicate that private boat fishing in the state usarly doubled between 1%8 and 1973 (Miller 1980). Although only limited data are available
~
-on sport fishing in the New Jersey waters of the Delaware system, data available for Delaware waters indicate recreational fishing has been increasing rapidly in accord with the national trend (Lesser 1972; L
Martin 1973; Miller 1977; McHugh 1981). l l_ Based on aerial surveys, the man-days of sport fishing by private boats in Delaware waters increased from'approximately 192,000 in 1971 to O* ' 256,000 -in 1976 (Martin 1973; Miller 1977) . Party boats exerted another 95,800 man-days of fishing ef fort in the Delaware River and Bay in 1976 l l 2.6-3 l
a - Salem 316(b) Demonstration (Miller 1977) . In 1978, approximately 107,000 man-days of sportfishing - m e effort were exerted by private boats; however, these data were collec-ted by different sampling techniques and do not necessarily indicate a h E iE decrease (Miller 1980). Recreational fishing effort by shore fishermen % e in Delaware increased from approximately 74,000 man-days in 1971 (Martin 1973) to 133,000 man-days in 1976 (Miller 1977) . L $ The projected total recreational catch in Delaware waters has fluctuated j over the years. It was estimated as 2,363,000 fish in 1968, 1,948,000 in 1973, 5,817,000 in 1976, 2,096,000 in 1978 (Miller 1977, 1980), and 3,241,000 in 1979 (NMFS 1980). f Similarly, the average catch per man-day has fluctuated randomly in g recent years. Catch rates were 7.5 finh/ day in 1968,12.4 in 1971, 5.6 in 1972, 3.9 in 1973,10.0 in 1976, and 7.4 in 1978 (Miller 1977, 1980). Seagraves (1981) calculated the average catch rates for July and August E in 1980 and 1981 to be 6.6 and 3.6 fish / day, respectively. 1 Since 1968, weakfish (Cynoscion rezalis) have typically dominated
= the recreational finfish catch in Delaware Bay waters (Miller 1980).
f The annual percentage of the total number caught has ranged from a low _ _ of 28.5 percent in 1978 (Miller 1980) to a high of 80 percent in 1980 b (Seagraves 1981). Summer flounder (Paralichthys dentatus) and Atlantic i croaker (Micropogonias undulatus) were generally the second or third most common species caught in this region, followed by bluefish , 4 (Pomatomus saltstrix) and sharks of several species (Miller 1980; [ Seagraves 1981). h .. - In 1974, the Delaware recreational finfish catch weighed approximately
/ 2,900,000 kg (McFugh 1981). The catch consisted of approximately -
1 1,700,000 kg'veakfish, 227,000 kg bluefish, 84,000 kg sharks, 69,50n . kg summer flounder, and 227,000 kg other fishes (McHugh 1981). These ( figures indicate that the recreational finfish catch in Delaware may be substantially higber than the commercial catch (McHugh 1981). n Recreational fiafishing on the Delaware River in the vicinity of Arti-I :t ficial Island generally is limited to pan-sized white perch (Morone i americana), striped bass (Morone saxatilis), and weakfish (IA 1977). j Larger striped bass (up to 2.27 kg) and small (12.7-17.8 cm) bluefish { are sometimes caught south of Artificial Island. Adult bluefish and - weakfish also are taken occasionally (IA 1977). Several species of -3 y catfish, American eel (Annui11a rostrata), and carp (Cyprinus carpio) { are taken along this stretch of the river by bridge and shore fishermen - Q (IA 1977). . 6 In addition, seasonal sport finfisheries for American shad (Alosa sapi-E' dissima) and O.ewives (Alosa pseudoharengus or Alosa aestivalis) exist g on the Delaware River. Shad are taken by recreational fishermen in March-April, and a 1974 survey indicated approximately 72,000 man-days L. h of effort on the Delaware River (Appendix III, DBFWMC 1980). A substan-tial hook-and-line fishery for alewives exists on the Delaware River h 1 during spring migration runs, centered around Trenton (Appendix V). = 2.6-4 w K h-' ..!
)
Salem 316(b) Dem nstrction l l I Shellfish Recreational Fisheries
'The blue crab is an important recreational species in the Delaware River, Bay, and C&D Canal (Homa 1978). Surveys in Delaware waters
- indicated that 38 percent of the recreational fishermen in 1978 also participated in crabbing (Miller 1980). With an average harvest of 19 crabs a day, the total seasonal catch was over 1,000,000 blue crab (Miller 1980). In 1976, an estimated 639,018 crabs were taken by the Delaware registered boaters, but no estimate could be derived for the total number taken in the Delaware Bay (Miller 1980).
There is also an active sport fishery for blue crab during the summer I and early fall on the section of the Delaware River adjacent to Arti-ficial Island (IA~1977). Unfortunately, altbough data are available concerning the commercial blue crab fishery along this section of the River, no quantitative dets on recreational crabbing exists. Recreational Boatine
!- No quantitative data concerning recreational boat traffic on the Dels-ware River and Bay are available (U.S. ACE 1975a). However, the sale of boat licenses gives an indication of the increasing popularity of l boating for recreation. Over 150,000 boat licenses were sold ~in Dels-ware in 1970; this does not include sailboats without motors, rowboats, canoes, or passenger boats such as party fishing and diving boats ,j (Coastal Zone of Delaware 1972). Furthermore, sales in Delaware are D expected to increase 32 percent by the year 2000 (Coastal Zone of Delaware 1972). !
Because Delaware is easily reached from neighboring states and because it has a relatively large coastline, a great number of nonresidents launch their boats in Delaware (Coastal Zone of Delaware 1972). A survey of public boat access sites in Delaware indicated that 44 per-cent of cars parked at access sites were nonresidents, primarily from Pennsylvania and Maryland (Lesser 1972). There also are numerous boat launching sites along the River in New Jersey and Pennsylvania. Boating in the Delaware estuary usually is done in combination with other recreational activities such as fishing, racing, swinsning, diving, sunbathing, picnicking, sightseeing, and camping (Coastal Zone of Dela-were 1972). Data from Delaware estimate that approximately 95 percent of all reerestional boating activities are connected with fishing , (Lesser 1%8). 7 As with fishing, the heaviest recreational boating activity occurs l in Delaware Bay (U.S. ACE 1975b). There is very little recreational boating activity in the Philadelphia area, but the use of the River for pleasure boating rapidly' increases above and below Philadelphia (U.S. ACE 1975b). LO 2.6-5
- - - . . - - _ . _ - - - - ._ - - , ~ . - - . -
Salem 316(b) Dem:nstrction 2.6.2.2 Commercial. Industrial. and Municipal Uses Finfish Commercial Fisheries O The seasonality of the fishery and the lack of catch-reporting require-ments make it difficult to estimate the magnitude of the finfish commer-cial fishery in the Delaware estuary (Seagraves 1981). Based on random interview, landing data, and logbooks kept by commercial fishermen in Delaware, the 1980 and 1981 commercial catches in Delaware Bay were estimated to be approximately 546,000 and 706,000 kg, respectively (Seagraves 1980, 1981). Weakfish have dominated the catch since 1976, constituting 73 percent of the total commercial catch in 1980 and 68 percent in 1981 (NOAA 1977; NMFS 1977, 1978, 1979; Seagraves 1980, 1981). Other important species caught since 1976 include bluefish, carp, American shad, striped bass, white perch, American eel, and menhaden. Because these data come from landings, species caught outside the Bay and brought to a port within the Bay are included. Some of the menhaden catch probably did come from outside the Bay, but the menhaden population has rebounded in recent years to account for approximately 25 percent of the commerical catch in the lower estuary in the early 1970s (Tyranski 1979). Other his-torically important commercial species in the Delaware River include alewives, Atlantic sturgeon (Acipenser oxyrhynchus), Atlantic croaker, and spot (Leisotomus xanthurus) (McHugh 1981). These species all have shown major fluctuations in abundance or availability and recently have not been important commercial species (Seagraves 1980, 1981). g Only a limited commercial finfishery exists on the Delaware River adja-cent to Artificial Island (IA 1977). Species caught most frequently include American shad, striped bass, American eel, various species of catfish, and carp (IA 1977). Eel are fished from March through Novem-ber, shad and bass from March through May, catfish during the fall sea-son, and perch and carp are fished from October through May (IA 1977). Shellfish Commercial Fisheries The blue crab is the largest commercial fishery in the Delaware estuary (Homa 1978; McHugh 1981). However, as is characteristic of a species near the northern limits of its range, blue crab have exhibited great variations in abundance in the Delaware Bay (McHugh 1981). After a har-vest of nearly 2,300,000 kg in 1957, landings dropped to about 91,000 kg in 1968 (McHugh 1981). Availability of blue crab increased again in 1975 and 1976 when approximately 1,600,000 kg were harvested (McHugh 1981). Af ter a prolonged period of unusually low temperature in the winter of 1976-1977, the catch declined to only 528,000 kg (NMFS 1977; Homa 1978). Recently, blue crab again have become abundant in the Delaware Bay; the 1980 catch was approximately 1,500,000 kg (NMFS 1980). l Adjacent to Artificial Island, the Delaware River supports a substantial blue crab commercial fishery. Estimates of the hard crab catch from this commercial region range from 315,000 kg in 1971 to 945,000 kg in 1975 (PSE&G 1978) . During the 1976 season, 50 licensed commercial crabbers operated in the area; 25 were based in New Jersey and 25 in 2.6-6
Salem 316(b) Dem:nstration Delaware (Meadows 1977). The total catch of hard crabs from this region of the River exceeded 32,500 bushels, or 680,000 kg (Meadows 1977).
.O In addition, approximately 39,000 kg of peeler crabs were harvested l (Meadows 1977). The estimated dockside value of all crab taken near '
Artificial Island in 1976 was $474,000 (Homa 1978).
'In 1977, 41 licensed crabbers operated in the vicinity of Artificial Island-20 from New Jersey and 21 based in Delaware (PSE&G 1978). After the unuous11y cold winter of 1976-1977, the hard crab catch in this ares ,
declined to only 140,000 kg (PSE&G 1978). The peeler crab catch taken i in the area was approximately 9,000 kg (PSE&G 1978). All the blue crab l taken near Artificial Island in 1977 were worth approximately $128,000 (PSE&G 1978). Industrial and Municinal Discharmes ( The Delaware River and Bay receive wastewaters from a number of munic- ; 4 ipal and industrial sources. There are more than 80 known point-source dischargers in the Delaware estuary (DRBC 1983). Delaware River Basin Commission's (DBRC) regulations specify water quality standards on discharges from individual point sources and effluent limitations for a stacific geographic zones in the Basin. These include maximum allow-sole wasteload in pounds of biological oxygen demand (BOD) for each of the major dischargers. In addition, the Nations 1 Pollutant Discharge Elimination System (NPDES) program requires technology 4ar?d or sater-quality-based effluent limitations for each discharge. In the vicinity of Sales, the States of New Jersey, Pennsylvania, and Delaware admin-i ister the NPDES program and related state statutes to regulate these discharges. The DRBC wasteload allocations limit discharges to the Delaware estuary
- to a total of 151,000 kg of BOD per day (DRBC 1983). Approximately 52 percent of the total oxygen demand in the Delaware estuary is contrib-uted by nuncipalities, about 26 percent by industry, and the remaining 22 percent by tributary and stormwater overflow (Kiry 1974). When the Philadelphia, Trenton, and Camden sewage treatment plants are upgraded in the mid-1980s, the DRBC overall wasteload allocation requirements for the Delsware estuary, in general, will be met (DRBC 1981).
Through the efforts of DRBC, the state agencies administering the NPDES program, and various municipal and industrial sources in the area, water quality in the Delaware River and Bay has improved over the last several years (DRBC 1981). However, dissolved oxygen concentrations still have been below DRBC water quality standards in certain reaches of the River j during the summer of recent years (DRBC 1981). Following improvement of i the Philadelphia, Trenton, and Camden sewage plants, and implementation of more stringent effluent limitations based on "best available technol-ogy," further improvements in water quality may d, pend on the treatment of nonpoint sources such as storm runoff (DRBC 1981). 2.6.2.3 Transoortation The Delaware River provides a commercial route for waterborne commerce from Trenton, New Jersey, to the Atlantic Ocean. Ports are located 2.6-7
Salem 316(b) Demonstrction along both sides of the Delaware River and Bay from Delaware City to Trenton. The U.S. ACE (oastal Zone of Delaware 1972) lists 16 ports as significant handlers of waterborne commerce. The three most important h harbor areas are Philadelphia, Trenton, and Wilmington (U.S. ACE 1978). In 1978, over 132,400,000 tons of freight were moved on the Delaware River between Trenton and the sea, including approximately 102,100,000 tons of ocean-going traf fic and 30,300,000 tons of internal traffic (U.S. ACE 1978). The majority of freight traffic on the Delaware River in 1978 was foreign imports (approximately 67,120,000 tons) (U.S. ACE 1978). The major commodities handled on the Delaware (in order of decreasing tonnage) are petroleum products, iron ore and concentrates, and corn (U.S. ACE 1978). In 1978, Philadelphia handled over 50,800,00 tons of freight traffic, primarily foreign impor" of crude petroleum; Trenton handled 890,000 tons, primarily domest N receipts of coal and lignite; Wilmington handled approximately 3,300,000 tons of mostly domestic internal receipts of distillate fuel oil and residual fuel oil, foreign imports of residual fuel oil, and domestic coastwise shipments of gaso-line (U.S. ACE 1978). Over 14,500,000 tons of freight traf fic were shipped via the C&D Canal in 1978 and traveled through Delaware Bay (U.S. ACE 1978). Approxi-mately 7,400 vessels traveled eastbound through the Canal and 6,800 vessels traveled westbound through the Canal, into the Chesapeake Bay (U.S. ACE 1978). For transatlantic ships, Baltimore is 185 km nearer Europe via the C&D Canal than around the Virginia capes. For vessels g traveling between Baltimore and Philadelphia, the Canal route is 460 km shorter (Coastal Zone of Delaware 1972). To facilitate navigation on the Delaware River, a 214-km-long man-made navigation channel is maintained (U.S. ACE 1975a). In its natural state, the River from Philadelphia to the Atlantic Ocean had a control-ling depth of approximately 5 m. From Trenton to Philadelphia, the River was narrow, winding, and obstructed by shoals with a natural depth of only 1.0-2.5 m (U.S. ACE 1975a). Improvements to the River were first authorized by the U.S. Congress in 1836 and since then about 765,000,000 m3 of material has been removed (U.S. ACE 1975a). Federal navigation projects currently provide for a 12-m-deep channel from the sea for 203.5 km to Newbold Island and a 11-m-deep channel for 9 km to ! the Trenton Marine Terminal (Homa 1978). Because 1,400,000 tons of sediment are deposited annually in the tidal Delaware, maintenance dredging of the navigational channel is a nearly continuous process (U.S. ACE 1975a). ihe U.S. Army Corps of Engineers removes over 6,273,000 m3 of spoil r.nnually from the Delaware River, Schuylkill River, and Wilmington Harbor. Private dredging removes another 1,759,500 m3 annually (U.S. ACE 1975a). ( Large-scale navigational dredging activities can temporarily disrupt benthic communities, increase turbidity, and create flow patterns that af fect salinity; however, the primary concern with dredging in the Dela-h ware River has been with spoil disposal (Daiber et al.1976). Pumping 2.6-8
Sclem 316(b) Demsnstration spoil into adjacent underwater sites may harm the estuarine ecosystem due to increased turbidity, decreased light penetration, decreased algal productivity, increased oxygen demand, and the reintroduction of toxic materials such as heavy metals that may be present in bottom sediments (Daiber et al.1976). Spoil disposal in wetlands can affect these habitats adversely by altering the local topography, chemical composi-tion, and drainage patterns, and suffocating the submergent or emergent vegetation (U.S. ACE 1975b). Disposal of dredged material on lowland or uplaud sites can cause habitat destruction and the temporary exclusion of other land uses (U.S. ACE 1975b). Overall, the environmental effects of each dredging operation depend on the season, the duration of the dredging operation, the amount of spoil, the spoil disposal site, and the mode of dredging (Daiber et al. 1976). During the U.S. Army Corps of Engineers' dredging operations in the Delaware River, dredge material generally is deposited in existing onshore banked sites (U.S. ACE 1975b). Consideration is given to the effects of the disposal site on the total environment of the region, including effects 6n fish and wildlife, water quality, and estuarine ecology (U.S. ACE 1975b). 2.6.2.4 Water Supp1v The Delaware River and its tributaries provide a source of water for municipal and industrial use, including the generation of electricity. Total surf ace water withdrawals in the Delaware estuary in 1978 averaged /D 9,650 ED (DRBC 1981). In 1975, withdrawals by the major users totaled V 5,687 MGD (DRBC 1981). Most of the water is returned to the Delaware basin af ter treatment and is available for reuse (DRBC 1981). Depletive water uses permanently remove water from the estuary. The average depletive use of water from the Delaware Basin was 393 MGD in 1975, 458 MGD in 1980, and is expected to reach 568 FCD in 1985 (DRBC 1981). Most of this water is consumed by municipal wa6er suppliers and industry (DRBC 1981). n M 2.6-9
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- and Gas Company Salem 316(b) Demonstration pigu,e 1 s-1
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Salem 316(b) Demonstrction i LITERATURE CITED: SECTION 2 Barnes , R.D. 1968. Invertebrate Zoology. 2nd Ed. W.B. Saunders Co., Philadelphia. 743 pp. Coastal Zone of Delaware. 1972. Final Report of the Governor's Task Force on Marine and Coastal Affairs. University of Delaware, Newark. 464 pp. Cronin, L.E., J.C. Daiber, and E.M. Hulbert. 1962. Quantitative seasonal aspects of zooplankton in the Delaware River estuary. Chesapeake Sci. 3( 2):63-93 . Daiber, F.C. , L.L. Thornton, K. A. Bolster, T.G. Cambell, 0.W. Crichton, G.L. Esposito, D.R. Jones, and J.M. Tyrawski. 1976. An Atlas of Delaware's Wetlands and Estuarine Resources. Delaware Coastal Manage-ment Program, Technical Report 2. Delaware State Planning Office, Dover. 528 pp. Delaware Basin Fish and Wildlife Management Cooperative (DBFWMC). 1980. Strategic Management Plan for the American Shad (Alosa sanidissima) in the Delawara River Basin. Delaware River Basin Authority, Trenton, N.J. 132 pp. I Delaware River Basin Commission (DRBC). 1975. Water Management of the O Delaware River Basin. DRBC, West Trenton, N.J. Delaware River Basin Commission (DRBC). 1981. The Delaware River Basin Comprehensive (Level B) Study. DRBC, West Trenton, N.J. 153 pp. 4 Delaware River Basin Commission (DRBC). 1983. Current Status of Allocations, Delaware Estuary. January 1983. DRBC, West Trenton, N.J. l t Epifanio, C. 1979. University of Delaware. Personal communication to Ichthyological Associates. September. Ferrigno, F., L. Widjeskog, and S. Toth. 1973. Wetland ecology, marsh destruction. Job Progress Rept. , Project No. W-53-R-1, Job No. IG. New Jersey. Division of Fish, Game and She11 fisheries. 20 pp. i Roma, J., Jr. 1978. A study of the Delaware River from Reedy Point, Delaware, to Trenton, New Jersey, with Special Reference to the Shallows. Ichthyological Aasociates, Inc., Middletown, Del. 470 pp. p L Ichthyological Associates, Inc. (IA). 1977. An Ecological Study of the ! . Delaware River in the Vicinity of Artificial Island: Progress Report r 'for the Period January Through December,1976. Prepared for Public Service Electric and Gas. IA, Middletown, Del. .O 1-1 ? l
, - . . . , , . , - ~ , y,r- . - - - _
Scien 316(b) Dem:nstrctice Ketchum, B.H. 1953. Preliminary evaluation of the coastal water of f Delaware Bay for the disposal of industrial wastes. Reference 53-31. Woods Hole Oceanographic Institute, Woods Hole, Mass. Kiry, P.R. 1974. A Historical Look at the Water Quality of the Delaware River Estuary to 1973. Academy of Natural Science, Depart-ment of Limnology, Philadelphia. 76 pp. Lesser, c.A. 1968. Marine Fisherier Survey. Delaware Game and Fish Commission, Dover. 21 pp. Lesser, C.A. 1972. Sport Fishing Survey of the Delaware Estuary: 1971. Delaware Division of Fish and Wildlife, Dover. 11 pp. Lynch, J. 1979. Ichthyological Associates. Personal communication. September. Martin, C.C. 1973. Sport Fishing Survey of the Delaware Estuary.- Federal Aid Fiaheries Restoration Project F-24-R (D-J) Final Report. Delaware Division of Fish and Wildlife, Dover. McHugh, J.L. 1981. Marine fisheries of Delaware. Fish. Bull. 79(4):575-599. Meadows, R.E. 1977. The biology and economics of the blue crab, callinectes sapidus, in An Ecological Study of the Delaware River in the Vicinity of Artificial Island: Progress Report for Peri 9d Janucry llh through December,1976. Ichthyological Associates, Inc., Middletown, Del. Miller, R.J. 1970. Distribution and Energetics of an Estuarine Popu-lation of the Ctenophore, Mnemiopsis leidvi. Ph.D. thesis. North Carolina State University, Raleigh. 78 pp. Miller, R.N. 1977. Marine Recreational Fishing in Delaware. Federal Aid Fisheries Restoration Project F-29-R (D-J). Document 40-50/78/ 01/18. Delaware Division of Fish and Wildlife, Dover. 27 pp. Miller, R.N. 1980. Delaware Sport Fishing Survey. Federal Aid Fisheries Restoration Project F-29-R (D-J). Document 40-50/80/ 03/02. Delaware Division of Fish and Wildlife, Dover. National Marine Fisheries Service (NMFS). 1977. Annual Landings by State, County, and Species. Data Management and Statistic Division, NMFS, Washington, D.C. National Marine Fisheries Service (NMFS). 1978. Annual Landings by State, County, and Species. Data Management and Statistic Division. NMFS, Washington, D.C. National Marine Fisheries Service (NMFS). 1979. Annual Landings by State, County, and Species. Data Management and Statistic Division. NMFS, Washington, D.C. lh
_ .- _ _ _ ~ _ _ _. .
. S21em 316(b) Dem::nstration National Marine Fisheries Service (NMFS). 1980. Annual Landings by State, County, and Species. Data Management and Statistic Division, NMFS, Washington, D.C.
National Oceanic and Atmospheric Administration (NOAA). 1977. New Jersey Landings Annual Summary, 1976. Current Fisheries Statistics No. 7213. Washington, D.C. National Oceanographic and Atmospheric Administration (NOAA). 1982. Tide Tables. High and Low Water Predictions: East Coast of North and South American Including Greenland. 285 pp. Odum, E.P. 1971. Fundamentals of Ecology, 3rd Edition. W.B. Saunders Co. 574 pp. Pape, E.H. and R.W. Garvine. 1982. The subtidal circulation in Delevare Bay and adjacent shelf waters. J. Geophys. Res. 87(C10):
-7955-7970.
Pennock, J.R., J.H. Sharp, and W.J. Cazonier. 1983. Phytoplankton, h The Delaware Estuary: Research as Background for Estuarine Management and Development (J.H. Sharp, ed.), pp. 133-155. Univereity of Delaware, Lewes. 311 pp. Polis, D.F. and S.J. Kupferman. 1973. Physical Oceanography. Delaware Bay Report Series, Volume 4. University of Delaware, Newark. 136 pp. plus appendix. Pritchard, D.W. and G.B. Gardner. 1974. Hydrography of the Chesapeake and Delaware Canal.' Chesapeake Bay Institute, Johns Hopkins University, Baltimore. Tech. Rep. No. 85:1-171. < Public Service Electric and Gas Company (PSE&G). 1980. An Ecological Study of the Delaware River near Artificial Island, 1 % 8-1976: A Summary. PSE&G, Newark, N.J. Public Service Electric and Gas (PSE&G). 1978. Annual Environmental Operating Report (Nonradiological). Salem Nuclear Generating Station. Unit No. 1. Volume 2. PSE&G, Newark, N.J. Roy F. Weston, Inc. (Weston). 1982. Near-field and far-field current velocity and circulation studies in the vicinity of the Salem Nuclear Generating Station, Delaware River Estuary. Prepared for Public Service Electric and Gas Company. Weston, Newark, N.J. 76 pp. plus appendixes. Salter, M. 1973. Net transport of water through the mouth of Delaware
- l. Bay, h Physical Oceanography (D.F. Polis and S.L. Kupferman, eds.),
l pp. 137-143. Delaware Bay Report Series Volume 4. University of f Delaware, Newark. [ Seagraves, R.J. 1980. Annual Report of Catch and Effort Statistics, Part II. Delaware Division of Fish and Wildlife, Dover.
,,------------r------r -m-~,
- . , . ,,e ,.,,,,c ,,----,,--p, .m-e, e-, ,,,m,-,pm ,---,-,,--,em--gmwm-g--ge-w--vn,-,--w-e-,
Salem 316(b) Dem:nstrctica Seagraves, R.J. 1981. Annual Report of Catch and Effort Statistics, Part II. Delaware Division of rish and Wildlife, Dover. Stroud, R.H. 1977. Changing Cna11enges in Recreational Fisheries. SFI Bulletin 284, Washington, D.C. 8 pp. (Cited in Miller 1977). Swain, F.W. 1972. Biogeochemistry of Sediments of Delaware Bay. College of Marine Studies, University of Delaware, Newark. 44 pp. Truitt, R.V. 1939. Our water resources and their conservation. Chesapeake Biol. Lab., Solomons, Md. 103 pp. Tyranski, J.M. 1979. Shallows of the Delaware River from Trenton, New Jersey, to Reedy Point, Delaware. U.S. Army Corps of Engineers, Philadelphia District, Philadelphia. 519 pp. U.S. Army Corps of Engineers (U.S. ACE). 1975a. Delaware River, Trenton to the Sea and Schuylkill River and Wilmington Harbor Tributaries. Final Composite Environmental Impact Statement, Project Maintenance, New Jersey, Pennsylvania, Maryland. Philadelphia District, Philadelphia. U.S. Army Corpa of Engineers (U.S. ACE). 1975b. Final Environmental Impact Statement, Project Maintenance: Delaware River, Trenton to the Sea, and Schuylkill River and Wilmington Harbor Tributaries. , Philadelphia District, Philadelphia. U.S. Army Corps of Engineers (U.S. ACE). 1978. Waterborne Commerce of O the United States, Part I: Waterways and Harbors, Atlantic Coast. U.S. ACE, Washington, D.C. 198 pp. U.S. Geological Survey (USGS) . 1966. Observations of Tidal Flow in the Delaware River, Geological Survey Water-Supply Paper 1586C. U.S. Geological Survey (USGS). 1971 - 1983. Water Resources Data for Pennsylvania Water Year 1975. USGS Water-Data Report No. PA-71-1 to PA 81-1. Eleven volumes. U.S. Geological Survey (USGS). 1981a. Delaware River Basin: Vol. I af. Water Resources Data for Pennsylvania. USGS Water-Data Report No. PA-GO-1. 287 pp. U.S. Geological Survey (USGS). 1981b. Delaware River Basin and tribu-taries to Delaware Bay: Vol. 1 of. Water Resources for New Jersey, USGS Water-Data Report No. NJ-80-2. 287 pp. Malton, T.E., III, and R. Patrick (eds.). 1973. The Delaware Estuary System, environmental impacts and socio-economic effects; Delaware River estuarine marsh survey. A report of the Nat. Sci. Found. RANN Program, Acad. Nat. Sci. Philadelphia, University of Delaware, Rutgers University. 174 pp. Ward, R.F. 1958. Geology of the Delaware River. Estaarine Bull. 3(3):4-9. ~
i Salem 316(b) Demonstration 4 1 s l l b 1 l i SECTION 3:
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il THE SALDi STATION t ( P l i l f 1
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Q Salem 316(b) Demonstration SECTION 3:
* /
THE SALEM STATION Page LIST OF TABLES LIST OF FIGURES 3.1 THE SITE AND ITS SURROUNDINGS 3.1-1 3.2 SALEM STATION 3.2-1 3.3 COOLING WATER SYSTEMS 3.3-1 3.3.1 circulating Water System 3.3-1 3.3.1.1 Original CWS Intake Structure 3.3-2 3.3.1.2 Condensers 3.3-6 3.3 .1.3 Discharge 3.3-6 3 .3 .1.4 Pressure / Temperature / Time Relationships 3.3-6 3.3.2 Service Water System 3.3-7 3.3.2.1 Intake structure 3.3-7 3.3.2.2 Discharge 3.3-9 3.4 OPr. RATION OF SALEM STATION 3.4-1 LITERATURE CITED 9 V
4 I . Salem 316(b) Demonstration . l f l LIST OF TABLES: l SECTION 3 i i Nu:nber Title , 3.2-1 Principal features of Salem station identified in i i Figures 3.2-2 through 3.2-4. ! 3.4-1 Incremental costs at full load of oil, coal, and nucicar generating units. I t O 3 i' 1 1
. _ . . _ _ . _ _ _ . . _ . , . . _ _ _ _ . . - . _ _, _ , _ , _ . _ _ , _ _ . _ _ _ _ _ _ , - , . , , , _ _ . , _ _ _ _ , . _ , , _ . _,..,-,,,__m_,,_-,_____,,_,,,
Salem 316(b) Dem nstration LIST OF FIGURES: SECTION 3 f--)s ( Number Title 3.1-1 Site vicinity within 80 km. 3.1-2 Site vicinity within 8 km. 3.1-3 Site location map from USGS quadrangle. 3.1-4 Salem station layout. , 3.2-1 Simplified steam-electric cycle. 3.2-2 Aerial view of Salem, looking northeast. 3.2-3 Artist's rendering of Salem, looking southwest. 3.2-4 Cutaway view of Salem, looking southwest. 3.2-5 - Circulating water system - intake. 3.2-6 Main condenser, outlet end. 3.3-1 Station layout with cooling water piping arrangement. i (v) 3.3-2 Circulating water intake system. 3.3-3 Modified vertical traveling water screen, Salem CWS. 3.3-4 Fish-bucket-type screen basket assembly, Salem CWS. 3.3-5 Fish counting pool and by-pass system, Salem CWS. 3.3-6 Typical pressure / temperature / time profile for Salem station CWS. 3.3-7 Service water intake. 3.4-1 Average weekday peaks by week of year, 1982 data. 3.4-2 Daily load shape peak days. 3.4 Typical electric production planned maintenance schedule, November through October. v
Salem 316(b) Demonstration SECTION 3:
, , THE SALEM STATION 3.1 THE SITE AND ITS SURROUNDINGS
^
Salen Generating Station is located on a peninsula known as Artificial Island on the eastern shore of Delaware Bay about 80 km (50 mi) north-west of the mouth of the Bay and 48 km (30 mi) southwest of Philadelphia (Figures 3.1-1 and 3.1-2). The Army Corps of Engineers created this island in the first half of this century while dredging the shipping channel. Depositing the dredged spoil between two small sand bars, the Corps first built the island, and later connected it to the mainland forming the peninsula. p As one might expect from its history, Artificial Island's surf ace soils generally are hydraulic fill composed of clay, silt, sand, gravel, and some organic materials. This layer is 7.6-9.2 m (25-30 f t) thick and overlies a 1.5- to 3-m (5- to 10-f t) base of coarse sand and gravel that was the original river bottom. f The peninsula extends about one-third of the way across Delaware River, which is roughly 4 km (2.5 mi) wide at that point (Figure 3.1-2), and is quite flat, with an average elevation of about 2.7 m (9 f t) above mean sea level (Figure 3.1-3). During the construction of Artificial Island, the Corps of Engineers built a protective levee around most of the west-ern shore. No new dredged material has been added to the site by the g Corps for at least 15 years, although they own in excess of 1,700 acres in the vicinity of Salem and are holding the area for future dredge spoil deposition. l The northern tip of Artificial Island lies in Delaware, whereas the balance, where Sales station is located, lies in Lower Alloways Creek Township, New Jersey. Prominent features in the area sre the Chesapeake and Delsware Canal (5 km [3 mil to the northwest), Hope Creek Jetty (3 km [2 mil to the southeast), and Augustine Beach, Delaware (about 5 km [3 mil due west). The entire area is within the Delaware River's estuarine zone, as defined by the Delaware River Easin Commission. As noted, Saleu station is located on the southern end of Artificial Island. The site was selected with respect to several criteria includ-ing adequate acreage and distance removed from population centers, based on the requirements of the Atomic Energy Commission (AEC) (now the Nuclear Regulatory Commission [NRC]). Other considerations were ( availability of large volumes of cooling water, transmission facilities, i and site access for heavy equipment. The site is adjacent to another l generating facility owned by Public Service Electric and Gas Company (PSE&G), Hope Creek station. Together, the sites for these facilities encompass 740 acres of. land, including 220 acres for Salem station and 153 acres for. Hope Creek station. This land is bordered by the Delaware River (on two sides) and by extensive marshes and uplands (on the remaining two sides). O 3.1-1
- l. . . . . _ _ _ . . __ _ _ _ _.__._.______._____,______ _ _ __. _ _
Salem 316(b) Demonstration The remaining lands adjacent to Salem are zoned for industrial and residential / agricultural use but fall under wetlands acts that will restrict development. In addition to the generating station itself, the Salem site contains associated buildings and structures, an electrical switchyard, parking areas , roads , and equipment laydown areas (Figure 3.1-4) . Riprap and bulkhead protect the shore from erosion. The site contains little natural vegetation, and what does exist is primarily reed grass. O O 3.1-2
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- 1. Ci culating Water intake Structure
- 2. Service Water inrake Structure
- 3. 500 kv Svmtchyard
- 4. Chemical Tanks
- 5. Station Service Transforrners (6) and Main Transformers
- 6. Administration Facility
- 7. Turbine Building
- 8. Auxiiiary Building
- 9. Reactor Containments
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. (Q j Salem 316(b) Demonstration Figure 3.14 _ . _ . _ _ _ _ , _ . _ _ . _ , . _ . . _ . _ _ . _ .. _ _ _ _ . . . ~ . . _ - - - - . . , . - . . _ , _ . ,
Sales 316(b) Demonstration l 3.2 SALEM STATION on December 13, 1966, Public Service Electric and Gas Company, Phila-delphia Electric Company, Delmarva Power and Light Company, and Atlantic City Electric Company submitted to the Atomic Energy Commission an application to construct's nuclear power plant. Following AEC review and public hearings by the Atomic Safety and Licensing Board, AEC issued the necessary construction permits in 1968. Construction began in the same year-at the Artificial Island site in Salem County, New Jersey-with Unit No.1 going into commercial service in 1977 and Unit No. 2 following in 1981. Sales has a planned service life of about 40 years. The generation of electricity at any steam-electric plant, including Salem station, involves thrse basic steps. First, heat must be pro-duced to convert water into stema. Extremely high quality water is required to avoid corrosion and scaling. The necessary heat usually is produced by burning coal, oil, or natural gas, or through nuclear fission. Second, the energy in the steam must be converted into mechanical energy by allowing it to expand in a heat engine such as 4 turbine, causing it to turn. For the turbine to turn, there must be a difference between the temperature and pressure exerted by the steam at the inlet to the turbine and the temperature and pressure at the. turbine outlet. The greater the difference, the more energy is transferred. Finally, the mechanical energy of the rotating turbine must be converted into electrical energy. This is accomplished by using the turbine to turn a generator. Cooling water to flow through a condenser (Figure 3.2-1) is required to maximize the ef ficiency of this process. The cool temperature of the I cooling water relative to that of the steam as it leaves the turbine condenses the steam back into water, which occupies a much smaller volume than the steam. This, accordingly, reduces the outlet pressure on the turbine, allowing it to work more ef ficiently and allowing the generator to produce a greater quantity of electricity for a given amount of fuel. The lower the initial temperature of the cooling water, the more effectively the steam can condense, the lower the back pressure on the turbine, and the more efficiently electricity can be generated. In addition, both the high quality water resulting from condensing the steam and its residual heat energy are recycled, for it is returned to the heat source and once again converted into high-pressure steam to drive the turbine. In a steam-electric generatins plant, it is impossible not to waste heat from the condensing process to the environment. It should be stressed, however, that the lower the temperature at which the waste heat is rejected, the more efficient the process of energy conversion. This process is accomplished readily in an open-cycle, once-through, cooling system of the kind installed at Salem. The alternative, venting the exhaust steam from the turbine directly to the atmosphere, would waste both pure water and heat energy.
/"N The heat source for electrical generation at Salem is a pair of nearly h identical pressurized water reactors; each can produce about 3,400 MWe.
These reactors are housed in twin containment structures which rise 3.2-1
S:1ca 316(b) Demsnstrction to a height of about 58 m (190 f t) and are the nost prominent features of the Salem station. Water is pumped at high pressure through these reactors in closed loops to remova heat and transfer it through four heat exchangers called " steam generators." The steam generators consist of thousands of relatively small diameter tubes through which the heated reactor unter flows. Around the outside of these tubes flows the water to be converted to steam. It absorbs most of the heat of the reactor coolant, and because it is under less pressure than the reactor coolant, I this water is able to turn to steam. ] The steam is then transported through large diameter pipes to the station't two sets of turbines, which rotate as the steam passes through them to the lower-pressure areas beyond. The rotating turbines are connected to two electrical generators. Each of Salem's two electrical generating units is able to produce approximately 1,100 MWe. At Salem, the exhaust steam passes into each unit'3 three-shelled con-denser. These condensers consist of approximately 68,000 1-in. OD diameter tubes. Relatively low-temperature cooling water obtained from the Delaware River flows through these tubes, cooling the exhaust steam flowing past them. As the steam is cooled, it is condensed, regener-ated, and returned to the steam generators as feed water. When Salem is producing full power, the cooling water is returned to the Delaware River at a temperature approximately 100C warmer than when it entered the condenser system. These basic functions of Salem station are reflected in its physical structure and appearance. Figures 3.2-2 through 3.2-4 give an aerial perspective of Salem and are numbered to correspond to the features in Table 3.2-1. Figures 3.2-5 and 3.2-6 show the circulating water system (CWS) intake structures and the condensers. Salem's two most prominent features are the twin reactor-c"ontainment structures. Other major structures are the administrative, service, and auxiliary buildings, the turbine-generator area, the water-intake facility, and the electrical switchyard. PSE&G's intent was to incorporate within the design of the facility, features that blended with the surroundings as much as possible within the constraints imposed by the Station's primary function. The exter-nal surf aces of several major buildings are constructed of exposed-aggregate, precast concrete panels. The hemispherical-domed reactor containments and remaining buildings have a natural concrete finish accented by the exposed aggregate wall panels. Switchyard supports and structures are made of concrete, and the ground surf ace is leveled and covered with graded crushed rock to prevent veed growth and precip-itation puddling. The waterfront facilities (the circulating and service water intakes) have a low profile; major portions of these structures are continually submerged. Equipment in the exposed portions are enclosed to present a neat appearance. 3.2-2
Sclem 316(b) Demonstration Exposed nonconcrete buildings, equipment, end enclosures are painted light colors, primarily blue, to present a neat and pleasing appearance O' of blue and concrete gray. Also, the plant area is graded and land-scaped appropriately to enhance the appearance of Salem Generating Station. l l ] i (
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. Sclem 316(b) Demonstration TABLE 3.2-1 PRINCIPAL FEATURES OF SALEM STATION IDENTIFIED IN FIGURES 3.2-2 THROUGH 3.2-4
- 1. Reactor Containments
- 2. Turbine Building
- 3. Circulating Water Intake I
- 4. Service Water Intake '
- 5. Switchyard
- 6. Delaware River
- 7. Condenser Inlet
- 8. Condenser Outlet
- 9. Reactor
- 10. Steam Generator
- ! 11. Turbine
- 12. Generator
- 13. Circulating Water Discharge
- 14. Fish-Return Discharges (South not shown)
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i lp Salem 316(b) Demonstration - 1
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3.3- COOLING WATER SYSTEMS Salem's cooling water requirements are met by two systems: the circulating veter system (CWS) and the service water system (SWS). : These systems obtain cooling water from the Delaware River through two I independent intake structures. The CWS provides water to cool the main condensers. It requires water free of material capable of fouling or clogging the condenser tubes. The SWS is a safety-related system which is required to meet the rigid safety and performance standards of the Nuclear Regulatory Commission. It provides water to vital plant heat exchangers and coolers, but requires a smaller quantity of water than the CWS, 3.3.1 CIRCULATING WATER SYSTEM At Salem, the once-through CWS is the system designed to remove unwanted - heat from the condensers, as described in Section 3.2. The CWS with-draws cooling water from the Delaware River, routes it to the conden-sers, and ultimately returns warned water to the River. The primary components of the system are the cooling water intake, the pumps, the condensers, and the discharge (Figure 3.3-1). Salem's CWS was designed in the mid-1960s. Engineering considerations in the original design process, and reflected in the present system, include: G. 1. ' Efficiency--The amount of heat a given cooling system V must remove depends on the amount of heat contained in the turbine exhaust steam and the need to maintain tur-bine back pressure within the operational range. This, in turn, reflects the design of the steam turbine and the output of the heat source. The ability of a CWS to accomplish cooling depends on the volume and initial temperature of the water passing through it. These major components of the generation process--the heat source, turbine, and CWS--are integrally related and must be carefully matched to produce the desired electrical output efficiently.
- 2. Reliability--The system must provide cooling water under a wide range of environmental conditions for the station to operate efficiently at lesign capacity.
- 3. Constructability--The design must be able to be con-structed using acceptable engineering practices.
- 4. Operability-The system must be designed and constructed so as to require a minimum of operator attention. Des ign considerations include manpower necessary for operating, monitoring, and maintaining the equipment.
- 5. Maintainability--The equipment must be accessible and Os require minimum maintenance. Where this is not possible, duplicate equipment must be available.
3.3-1
Salem 316(b) Demonstration
- 6. Cost--As a regulated utility, PSE&G is obligated by New Jersey law (NJSA 44:2-23 and 48:3-1) to provide electrical service at reasonable cost. Acceptable cooling system designs, accordingly, are constrained ef fectively by the willingness of the New Jersey Board of Public Utilities and, ultimately , the electricity-consuming public to pay for them. In addition, the intake must be designed and constructed to be cost-ef fective.
The original design has been modified several times to provide greater protection to aquatic life in response to increasing environmental awareness. Bielegical and environmental considerations also entered into the location and original design of the entire station; the Atomic Energy Conmission required the preparation of safety analysis reports and environmental reports with defined contents; they reviewed them for acceptability. However, it was not until passage of the National Environmental Policy Act in 1969, and the Federal Water Pollution Con-trol Act in 1972, that specific techniques for measuring and criteria for evaluating the environmental ef fects of various cooling water system designs began to be developed. In response to the environmental concerns reflected by those statutes, and using the newly developed assessment methods and mitigative techniques, PSE&G instituted an ongoing review of possible changes to the CWS that would reduce poten-tial environmental effects. Between 1968 and the completion of the cooling system for Unit No. 1 in 1976, methods were examined to:
- 1. Reduce intake velocity and turbulence
- 2. Reduce fish impingement and improve survival
- 3. Reduce thermal plume recirculation
- 4. Determine the usage of the site area by aquatic species
- 5. Avoid construction during periods of high reproduction or rearing activity by aquatic life in the area After the initial CWS testing results were available in 1976, PSE&G took additional voluntary steps to:
- 1. Permit the survival of impinged fish by returning them to the River
- 2. Provide improved sampling research facilities to better understand and evaluate impingement and entrainment effects
- 3. Return debris to the River 4 Reduce recirculation of fish and debris 3.3.1.1 Original CWS Intake Structure The CWS intake, common to both Units No.1 and 2, was located at the extreme southern end of Artificial Island and consists of 12 separate, independent intake cells, 6 per unit (Figure 3.3-2) . The intake and discharge locations were finalized following the completion of hydro-thermal model studies aimed at miniaizing cooling-water recirculation.
O 3.3-2
- - .~ . . . - -
Salem 316(b) Demonstration _ Originally, each intake cell was equipped with its own removable ice ' - -[ ' - barrier, trash bars, wave wall, stop logs, traveling screen, and circu-lating water pump. The face of the intake was equipped with security alarms and fencing. The CWS intake was designed to operate at River levels between 81.0 and 100.5 f t PSD -(Public Service Datum is an arbitrarily assigned scale where station grade level is set at elevation 100 ft to avoid negative elevations within the station). River levels in. relation to PSD are: High high-water 97.5 ft PSD Mean high tide 92.2 ft PSD Mean tide and mean sea level 89.3 f t PSD Mean low tide 86.4 ft PSD Low low-water 81.0 ft PSD Ice Barriers i Removable ice barriers could be installed on the face of each of the
.12 intake cells to prevent damage during severe River icing conditions.
The barriers were constructed of pressure-treated lumber and were approximately 5.5 x 6.5 m (18 x 22 f t). They extended from elevation 100 to elevation 78 ft PSD. The barriers were resilient structures built to withstand the crush cf ice and to protect the trash bars. They were designed to be removed in early spring and replaced in late winter.
-/ 7 Trash Bars
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- Twelve sets of trash bars protected each of the 12 intake cells from large debris, mats of detritus, and other large materials commonly found in the River. The bar assemblies extended from station grade (100 ft PSD) to the bottom of each CWS intake cell (50 f t PSD) and were approx-imately 3 m (11 ft) wide. ' Constructed of 1.27-cm (0.5-in.) wide steel bars on 8.9-cm (3.5-in.) centers, the trash bar racks had a slot size of 7.6 cm (3 in.) wide by 15.5 m (51 f t) long.
The trash bars were inspected at least once per 8-hour shif t, and debris was removed as needed by a mobile mechanical trash rake. The rake was self-contained and traversed the entire intake width; it contained a trash hopper which transported the material removed from the bars to debris pits at each end of the intake. Baskets lined the pits and were removed as required. Debris was removed from trash bars and disposed offsite. Curtain Walls
-The original design of the intake structure had a curtain wall in '
front 'of the traveling screens to skim floating material from the surface of'the incoming water. It extended to the low low-water level (elevation 81.0 ft PSD). k 3.3-3
Salem 316(b) Dem:nstrction Original Traveling Screens Each intake cell is equipped with a vertical traveling screen. Each screen unit was a vertical, chain-link, 4-post type machine that oper-ated only when debris loads accumulated on the screen front and back. The traveling screens each contained 62 1-cm (0.4-in.) mesh screen baskets 307 x 53 cm (121 x 21 in.) with a reinforcing bar across the. center. As each screen panel reached the operation deck (elevation 100 f t PSD), organisms and debris were removed by a high-pressure 1 (100 psi) spray wash. Washing occurred on the front of the screen. Debris and organisms were washed into a single trough and conveyed to two baskets on the face of the intake structure. Period ically , , these baskets also serviced the trash rake on the intake structure's l face. No provision was made in the original design for returning fish or other material collected by the traveling screens to the River. CWS Pumps There are 12 CWS pumps located on the intake structure, one per cell, six per unit. They were manufactured by Worthington Pump Company and are of the vertical wet-pit type. Each is rated at 1.85 x 10) gpm at 8.2 m (27 ft) total dynamic head. The pumps are each powered by Allis Chalmers 2,000 hp, vertical shaf t motors, which run at 300 rpm. The once-through cooling water circuits from the intake to the discharge range from approximately 671 to 976 m (2,200-3,200 ft) in length (Figure 3.3-1). Water is supplied to the condensers in six separate 84-in. water lines per unit at a velocity of 3.2 m/sec (10.7 fps). Costs The cost of the original CWS intake structure through June 1976 was approximately $37,241,000 (based on cost as accrued). Modified Design At about the time Salem began commercial operation, PSE6G modified the CWS intake to allow survival of impinged organisms and pemit sampling l to assess impingement. , 1 Curtain Wall Modification and Wave Walls The bottoms of the curtain walls were removed in 1976 and 1977 due to concerns that their presence increased the approach velocities. Subse- I quent to the wall nodification it was found that heavy ice formation occurred on the traveling screens since they were now exposed to the 1 outside air temperature. The use of removable wave walls allows the interior of the building and the equipment to be heated, preventing icing. The removable wave walls are only installed during the winter. 3.3-4
Salem 316(b) Demsnstration Modified Travelina Screens b Each intake cell is now equipped with an automatic fish-removal type Q' . vertical traveling screen with fish buckets. The screens replaced the original conventional traveling screens. Each screen basket base was fitted with a 3.9-cm deep (1.5-in.) x 5.1-cm wide (2-in.) lip, which created a water-filled bucket (Figure 3.3-4) . As the basket is raised through and out of tne water, most impinged organisms drop of f the screen-into the bucket, which catches most organisms and prevents them from falling back into the screen well and becoming reimpinged. It then transports .them to a fish-return system (Figure 3.3-5) which returns the 1 organisms to the River. Normal operation was modified from intermittent to a continuous speed of 2.3 cm/sec (0.9 in./sec). Screens have alter-nate speeds 'of 4.8, 6.4, and 8.9 cm/sec (1.9, 2.5, and 2.5 in./sec) depending on debris load. For maximum fish survival, the screen wash was redesigned with low-pressure spray headers, and one"high-pressure spray header, in service. At high debris loads, the screen travel speed increases automatically to the second speed and a second high-pressure wash header is placed into operation. If the debris load continues to increase, the screen proceeds to he third speed. Any further increase causes an clarm to sound and the screen travel speed to increase to the fourth speed. The operators may take other necessary action. Transport time of individual screen baskets, from the water surface to the head sprocket at minimum screen speen, varies from 3.25 minutes at mean high water to 4.5 minutes at mean low water. As the screen basket. travels over the head sprocket, y organisms slide into the screen face and are washed by one low pressure (7 psi) spray header located outside the screen unit, and two low-
. pressure (15 psi) spray headers located inside the screen unit, into a new upper 38 x 75-cm (15 x 30-in.) sluice. This spray wash is designed to minimize descaling and other injuries that would occur with conven-
~ tional high-pressure spray headers (White and Brehmer 1976). Subse-quently, heavier debris is _ washed into a lower 60 x 146-cm -(24 x 58-in.)
sluice by two high-pressure (90 psi) spray headers (Figure 3.3-3). Fish-Return System The contents of the upper fish and lower debris sluices are returned to the River through one of two new return sluices at opposite ends of the CWS intake. The northern screen-wash water-return sluice is about 22 m (73 f t) lo'ag- and discharges to the -River at 1.5 m (5 f t) below mean icw water. The southern return sluice is also about 22 m (73 ft) long and discharges to the River about 1 m (3 f t) below mean low water. All screen-wash water could .be discharged only through one common outfall located at the northern end of the intake structure, while Unit No. 2 was being constructed. To redu recirculation of impinged fish and detritus on ebb tide, the second outfall was installed prior to Unit No. 2 operation at the southern end of the intake structure and put into operation'on July 14, 1978. Cates were installed in the fish and trash troughs in the center and at
\,,, each end of the troughs to permit discharge in the direction of tidal flow. Comparison of impingement rates before and af ter the southern 3.3-5
Salem 316(b) Dem:nstration discharge became operational indicates that recirculation has been reduced cotsiderably. Impingement Study Facilities At both ands of the CWS intake, - fish-counting pool is located adjacent to the screen-wash water-return trough. Wash water returning to the River can be diverted into a fish-counting pool (Figure 3.3-5). Costs From June 1976 to April 1981, an additional sum of approximately $4,949,000 (based on cost as accrued) was expended on improvements. These costs include only labor, materials, and subcontractor's expend itures . 3.3.1.2 Condensers One single-pass, divided-circulation, triple-shell condenser is located in each turbine building. The condensers, each of which is nominally rated at 1.924 x 109 kCal/hr (7.636 x 109 Btu /hr) and provides approx-imately 74,000 m2 (8 x 105 ft2) of cooling surf ace area. At full power, CWS flows of up to 4.2 m3/ min (1.1 x 106 gpm) per unit experience about a 100C temperature rise in the cooling water. The water passes through the 2.5-cm (1-in.) OD x 0.07-cm (0.028-in.) thick, 45-f t-long condenser tubes at an average velocity of about 2.3 m/sec (8 fps), then out of the outlet waterbox through u 2.44-m (90-in.) diameter connection. 3 .3 .1.3 Discharge Af ter exiting the condenser discharge, piping from each half of the condenser water box joins in a 3-m (10-f t) diameter pipe which runs to the River. The three pipes per unit convey the water approximately 152 m (500 f t) of f shore (Figure 3.3-1). The outlet of each of these pipes is at a depth of 7.6-9.1 m (25-30 ft). The exit velocity is high enough (10.7 fps) to promote rapid mixing with ambient water. The velocity, arrangement, and location are designed to reduce thermal recirculation. 3.3.1.4 Pressure / Temperature / Time Relationships The cooling water passing into the CWS intake structure, through the CWS pumps, through the condenser, and back to the Delaware River has various temperature and pressure changes impressed on it; these changes take a certain length of time to accomplish. During passage, the water and any organisms entrained in it experience temperature and pressure changes brought about by the system hydraulics and the added heat. Figure. 3.3-6 shows a typical pressure / temperature / time profile for the Salem station CWS. O 3.3-6
Salem 316(b) Dem:nstration 1 3.3.2 SERVICE WATER SYSTEM i (s_j The SWS is a safety-related system required for the safe operation and maintenance of Salem station. It provides strained Delaware River water to the coolers and heat exchangers located in the auxiliary, reactor, and Lerbine generator buildinga. This water does not come into contact with radioactive materials; it is returned to the River via the CWS discharge piping. As a safety-related system, the SWS meets the stringent requirements imposed by URC. The SWS is always in operation and is designed to
, provide an adequate cooling water supply to the reactor safeguard and auxiliary (quipment under all credible seismic, flood, drought, and storm conditions. The SWS for each unit is independent and not inter-connected except for the air compressors, dilution water for the intake hypochlorite system, and a common intake structure.
The SWS is designed to operate under a much wider range of River water levels than is the CWS: Lowest credible water 76.0 ft PSD Lowest low-water 81.0 ft PSD Low recorded water 83.1 ft PSD Mean low tide 86.4 ft PSD Mean tide 89.3 f t PSD Mean high tide 92.2 ft PSD High high-water 97.5 ft PSD -(()' Nominal site grade Flood water 100.0 ft PSD 112.0 ft PSD Maximum credible wave height 122.0 ft PSD 3.3.2.1 Intake Structure The SWS intake, constructed of reinforced concrete, is designed to withstand specific floods, earthquakes, and damage. It consists of 12 intake bays arranged in groups of three and alternating between Units No.1 and 2 (Figure 3.3-7) . Its internal compartments are designed to be watertight up to elevation 122 ft PSD. The intake, located at the River front, is fitted with ice barriers and marine dock bumpers and is designed to withstand the effects of tornadoes and missiles. Windbreaks are installed at elevation 112 f t PSD at the northern and southern ends of the structure. A heated enclosure with removable roof sections for maintenante and access is installed around the traveling screens and instrumentation. The intake is equipped with a fish-escape passage, located in front of the traveling screens and behind the trash bars. The passage connects all SWS cells and exits through the front of the cofferdams at the ends of the intake. v 3.3-7
Salem 316(b) Demonstrction Ice Barriers Because of the saf ety-related nature of the SWS intake, the ice barriers are always in place. The barriers extend from ths operating deck (ele-vation 112 ft PSD) to elevation 83.1 ft PSD. They are constructed in the same manner as the CWS ice barrier. Trash Bars The SWS trash bars are constructed in a similar manner as the CWS trash Sars, with 1.27-ca-wide (0.5-in.) steel bars set on 8.9-cm (3.5-in.) centers. However, SWS trash bars are 2.4-m (8-f t) wide and 12.8-m (42-ft) long. The SWS intake is serviced by one mechanical trash rake similar to CWS. The trash rake is mounted on rails on top of the deck at elevation 112 f t and can be positioned over any of the 12 bays. Curtain Wall The curtain valls are installed within each intake cell to provide protection from floating oil and fires. They extend from the operating deck (elevation 112 ft PSD) down to "lovest low-water" (elevation 81 ft PSD). - Traveling Screens Each pump cell is provided with a vertical traveling screen that extends from the bottom of the cell at elevation 70 f t PSD to the service deck at elevation 112 ft PSD. The screens are chain-driven by an electric motor mounted on top of the housing. The SWS intake screens are washed on the front side with a single series of high-pressure sprays to ensure that there is no clogging or fouling of the system. The 49 baskets per screen are equipped with 1-cm (3/ 8-in. ) mesh. The screens operate intermittently at a single speed, controlled by differential pressure across the screen face. When not in the cleaning mode, they remain at rest. Debris collected in troughs in the deck at the 112-ft elevation is transferred to trash baskets at either end of the intake. SWS Fumps Twelve vertical, deepvell turbine pumps are installed inside independent intake cells. There are six vertical, deepwell turbine pumps per unit manufactured by Lagne and Bowler. Each pump is designed with a capacity of 10,875 gpm at a pump head of 73 m (240 ft). The pumps are driven by Allis Chalmers vertical, solid-state, open-dripproof, air-cooled motors, each rated at 1,000 hp at 1,187 rpm. During normal operation, four pumps are in service. O 3.3-8
l Salem 316(b) Demonstration Automatic Strainer q,) Downstream of each SWS pump is located an automatic strainer. There are six strainers per unit, each manuf actured by the R.P. Adams Company.
. The design flow is 12,500 gpm per strainer at a design pressure of 200 Psig. The strain mesh size is 0.25 mm (0.010 in.) and is constructed of stainless steel. The s*rainers are continuously washed, and wash water is combined and routed to a yard drain that discharges to the River.
Costs The cost of the SWS intake structure through April 1981 was approxi-mately $15,784,000. These costs include on?.y labor, materials, and subcontractor's expenditures and are based on cost ledgers and the project control system. Costs of engineering, design work, overheads, or maintenance t*e not included in the estimate. Costs are as accrued. 3.3.2.2 Discharge Service water is continuous and is released to the CWS system, where it is returned to the Delaware River. O)
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Salen 316(b) Densnstration 3.4 OPERATION OF SALEM STATION The electricity generated at Salen is supplied to the Pennsylvania / New Jersey / Maryland Interconnection (PJM). PJM pools the power of 11 utilities with approximately 500 generating units of all sizes, includ-ing 65 units totally or partially owned by PSE&G. Normally , however, not all the installed capacity is available to produce electricity. Normal maintenance outages , forced outages , and other generation con-straints result in the practical generating capacity of all partici-pating utilities to the grid being substantially lower. Drawing electrical power from PJM are just under 8,000,000 customers: homes, commercial establishments, offices, industrial operations, and municipalities. On the PSE&G system alone, there are over 1,700,000 customers. They expect, and are entitled to receive, electric service that is adequate and reliable. Supplying the needed electricity can be complicated, because the aggregate of electric demands varies on an annual, seasonal, monthly, and daily basis, as well as on an hourly basis throughout the day. Figure 3.4-1 shows how the annual peak daily demand on the PSE&G system fluctuates; Figure 3.4-2 shows how the aver-age weekday electric peak varies over the course of a year. Although these figures appear to be smooth, predictable curves (because they show changes in peak and average demand), they actually fluctuate constantly, as millions of consumers turn on and off an even larger number of elec-trical devices. These fluctuations in electrical demand can create a number of problems for those planning the production of electricity. For a variety of reasons, including system reliability, electric generating stations cannot be started or stopped instantly to respond to short-term changes in demand. Thus, it is necessary always to have more capacity on the line than needed to meet demand at a given time. The larger the amount of this extra generation capacity, or " spinning reserve," the greater - the system's operating reliability; but it also becomes more expensive and inefficient. To respond to the more gradual, but generally larger, fluctuations in aggregate electrical domand over a 24-hour cycle, system operators can take a number of steps within the available time. Steps can be taken to increase or decrease the output of some units that are already oper-ating. Also, there are some units known as " peaking units" that can be started and stopped more readily to track daily demand. Usually, these units are gas turbines or diesel generators. Finally, there is the problem of the very large, but gradual seasonal changes in electrical demand over an annual cycle. Sufficieat time usually exirts to manage these fluctuations by starting up or shutting down generating units. Decisions as to which units should be operated in this intermittent fashion are influenced largely by ecor.omic considerations. Some types of generating units, such as nuclear, have relatively low operating expenses as compared to coal- or oil-fired generating units. Such units are generally operated effectively as baseload units. On the other 3.4-1
Salem 316(b) Demonstration hand, since oil- and gas-fired units have relatively higher operating expenses but can be started faster than nuclear units, and since elec-tric demand requires that some units be operated on an intermittent basis, it is more economic to select those units for intermittent operation. Table 3.4-1 depicts the incremental cost of electric power on PJM. The incremental cost of electric power escalates dramatically as demand increases, and as more costly generating capacity must be dispatched to meet the Ic,ad. On the PSE&G system, electric demand typically is greatest at about 4 PM during the months of July, August, and September when large air-conditioning equipment is in service. It is necessary that sufficient electric generating capacity be available at that tia to meet this peak with adequate reserves. To minimize the need to construct or maintain otherwise unneeded electrical generating capacity just to meet this peak, electricity producers try to schedule necessary unit outages for maintenance, equipment replacement, and repair-and in the case of nuclear plants, refueling-during of f-peak seasons. Outage scheduling provides for adequate capacity always being available to meet demand and still perform routine maintenance. In the case of nuclear plants, the time required to consume nuclear fuel efficiently is also considered. While avoiding the economic and environmental consequences of installing and maintaining additional generating units during these outages is complex and exacting, PSE&G manages this problem as outlined in Figure 3.4-3, which chows a typical year's maintenance schedule for major ge.nerating units. Salem contributes about 10 percent of the total electrical generating capacity of the PSE&G system. Because Salem is a nuclear plant with relatively low operating costs and extended start-up procedures, it is economic to run the unit as a baseload plant-that is, to operate it at maximum capacity whenever feasible. Since the unit also provides a substantial portion of PSE&G's overall generating capacity, it is very important for it to operate during peak demand in the summer months. The incremental cost at full load of generating electricity at Salem during the 1983 summer peak was approximately 1.2 cents per kWh (Table 3.4-1). The incremental cost of electricity on PSE&G's system at the same time was more than 10 times higher,12.9 cents per kWh. It can be seen rcadily that PSE&G, PECO, Delmarva, and ACE electric consumers would pay a very high price wheneT,er the Salem units are unnecessarily down or required to operate at reduced capacity during this period. Salem must, however, be out of service periodically for normal mainte-nance and refueling. PSE&G attempts to " stagger" these normal outages during seasons of off-peak demand to avoid having too much capacity unavailable at any one time. The fuel used at Salem generally per-mits operation of each unit for about 18 months between refuelings. Refueling a unit takes approximately 10 weeks, during which time PSE&G attempta to perform other required maintenance as well. O 3.4-2
Salem 316(b) Den nstration Unscheduled or forced plant outages can reduce the station's fuel consumption and lengthen the time between refuelings. For each day O of forced outage, refueling can be delayed potentially by one day. Over a 3-year period, the corebined refueling outage period of the two Salen units is at least 40 weeks. During typical station operation, each Salem unit is operated normally with five circulating water pumps and a sixth pump and traveling screen shut off for maintenance. This has resulted in an average number of 5.3 pumps in operation for Unit No. I and 5.0 for Unit No. 2. The necessity of this lower pumping is, a result of two factors. First, the large quantities of riverborne detritus collected cn the screc.ns reduce through-screen capacities and increase wear on the mechanisms. Second, the traveling screens are operated continuously to reduce the duration of impingement and improve survival. Conversely, tbs number of circu-lating water pumps is reduced to one during a typical refueling outage, resulting in a ' substantial reduction of intake flow. For biological modeling purposes in Section 6, refueling was assumed to occur from March 15 through May 24 (spring) and from October 5 through December 14 (fall), and to occur for each unit at 18-month intervals. The service water pumps are essential to the safe operation of the station. Typically, four pumps per unit are operated at all times, with two pumps available as backup. .- Sales station is operated as a " base-load plant" which means that full-power aparation at all times is desirable. The average full-power operation for Unit No. I has been 1,050 MWe and 1,063 MWe for Unit O No. 2. These power levels result in average full-power delta temper-atures through the condensers of 9.00C (16.20F) for Unit No. I and 11.10C (20.00F) for Unit No. 2. These power levels, delta temperatures, and pumping rates are used to predict the station's effects on the primary target species as described in Section 4.2.2.2. To che extent future station operations do not sustain such operational levels continuously year by year, this Demon-stration overstates station effects. O 3.4-3
Solen 316(b) Descastration TABLE 3.4-1 INCREMENTAL COSTS AT FULL LOAD OF OIL, COAL, AND NUCLEAR GENERATING UNIT;(a) Cost Per KWh Bergen (oil) $ 0.0462/KWh Mercer Unit No. 1 (coal) 0.0255/KWh Mercer Unit No. 2 (coal) 0.0267/KWh Salem Unit No.1 (nuclear) 0.0122/KWh Salem Unit No. 2 (nuclear) 0.0098/KWh , AT ANNUAL PEAK PSE&G system $ 0.129/KWh (a) Data based on operation as of September 7,1983. O O h
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Bales 316(b) Demonstration . j LITERATURE CITED: SECTION 3 0 - White, J.C. and M.L. Brehmer. 1976. Eighteen-month evaluation of the Ristroph traveling fish screens, in. Third National Workshop on Entrainment and Impingement (L.D. Jensen, ed.), pp. 367-380. Ecological Analysts, Melville, N.Y. a G 5 0
Salem 316(b) Demonstration O l l l SECTION 4: THE SALE! STUDY PROGRAM O O
Salem 316(b) Demanstrctica SECTION 4: THE SALEM STUDY PROGRAM O Pane LIST OF PIGURES 4.1 SELECTION M STUDY ORGANISMS 4.1-1 4.1.1 Background 4.1-1 4.1.2 Selected Target Species 4.1-2 4.1.2.1 Weakfish 4.1-2 4.1.2.2 Bay Anchovy 4.1-2 4.1.2.3 White Perch 4.1-3 4.1.2.4 Striped Bass 4.1-3 4.1.2.5 Blueback Herring, Alewife, and American Shad 4.1-3 4.1.2.6 Spot 4.1-4 4.1.2.7 Atlantic Croaker 4.1-4 4.1.2.8 Opossum Shrimp (Neomysis americana) 4.1-4 4.1.2.9 Scud (Gammarus spp.) 4.1-4 4.1.3 The Role of Target Species 4.1-5 i 4.2 THE STUDY OBJECTIVES AND PLAN-OF-STUDY 4.2-1 4.2.1 Objectives 4.2-1 4.2.1.1 Entrainment and Impingement Studies 4.2-1 4.2.1.2 Population Studies 4.2-2 4.2.2 The Plan-of-Study 4.2-3 4.2.2.1 Original Plan-of-Study 4.2-3 l 4.2.2.2 "Second Year" Plan-of-Study 4.2-4 4.2.2.3 Final Plan-of-Study 4.2-4 4.3 WTRAINMENT AND IMPING MENT ABUNDAN0E AND SURVIVAL STUDIES 4.3-1 4.3.1 Entrainment 4.3-1 4.3.1.1 Entrainment Abundance 4.3-1 4.3.1.2 Entrainment Survival 4.3-2 4.3 .1.3 Entrainment Simulation 4.3-4
. 4.3.2 Impingement 4.3 -4 4.3.2.1 Impingement Abundance 4.3-4 4.3.2.2 Impingement Survival 4.3-6
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Sclem 316(b) Dem*,nstrction Page 4.4 FIELD STUDIES 4.4-1 4.4.1 The Stt.dy Area 4.4-1 4.4.2 Ichthyoplankton/Macroinvertebrate Field Program 4.4-1 4.4.2.1 Ichthyoplankton' Field Prog"am 4.4-1 4.4.2.2 Macroinvertebrate Field Program 4.4-2 4.4.3 The Juvenile and Adult Finfish Trawl Program 4.4-3 4.4.4 The White Perch Mark-Recapture Program 4.4-3 4.4.4.1 Mark-Recapture Field Program 4.4-4 4.4.4.2 Mark Evaluation Laboratory Studies 4.4-5 4.4.5 Age-and-Growth Studies of Larval and Juvenile Fish 4.4-5 4.4.6 Other Field Studies 4.4-6 LITERATURE CITED O O
Sales 316(b)'Demonstrction l i LIST OF FIGURES: SECTION 4 Number Title 4.3-1 Salem layout with entrainment abundance sampling locations. 4.3 -2 Location of CWS and SWS intakes, fish counting pool buildings, and SWS collection baskats. 4.3-3 Sampling strata in Artificial Island vertical profile transect, 1979-1980. 4.3-4 Strata sampled in the midbay vertical orofile transect, rka 37. 4.3-5 Strata sampled in the downbay vertical profile transect, rka 13. ] 4.3-6 Collection strata in finfish w-factor transect, rka 80. 4.4-1 Delaware River system from Cape May to Trenton, N.J. 4.4-2 Sampling strata for the Field Program in the Delaware River estuary,1981 and 1982. I 4.4-3 IP w-factor sampling transect, comprised of five offshore and one intake zone between Salem CWS and the Delaware shore. 4.4-4 Location of White Perch Mark-Recapture Zones in the Delawarv River. I
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Salem 316(b) Demonetrctica SECTION 4: THE SALEM STUDY PROGRAM, O This Demonstration summarizes the results of 15 years of environmental studies conducted by Public Service Electric and Gas Company (PSE&G) and its consultants on the Delaware system and the aquatic effects of Salem Generating Station. At various time's over that period, several govern-mental agencies and other groups have participated in designing and guiding these studies, and in analyzing the results. This section summarizes how the present study program evolved and how it focused on certain " target species" as those most likely to reflect any environ-mental effects of Saler station operation. It then explains how the study progres was designed to determine if any significant adverse effect occurs on target species, and describes the onsite and field investigations conducted. 4.1 SELECTION OF STUDY ORGANISMS 4.
1.1 BACKGROUND
Ecological studies in Delawar'e River and its tributaries in the vicin-ity of Salem began in April 1968. Early efforts were directed largely tovsed obtaining general, qualitative ecological information for various licensing documents (e.g., Salem Nuclear Generating Station Environmental Report-Operating License Stage [PSE&G 1971]). These I studies were the foundation for the more focused, detailed, quantitative i preoperational studies conducted in the early and mid-1970s. Data l collected from 1969 to 1976 by Ichthyological Associates (IA) provided I valuable information on important aspects of the local aquatic eco-system, and eventually were used by PSE&G in designing the operational aquatic ecology study program which was approved by the Nuclear Regula-tory Commission (NRC) and set forth in the Salen Environmental Technical Specifications (ETS) (Appendix B, Salen Generating Station--Operating License, DPR-70 and DPR-75) in effect at that time. The ETS aquatic studies for Salem began in late 1976, and were designed to provide data that could be compared with preoperational d.i.a to assess any ef fects of Salem on phytoplankton, microzooplankton, macro-zooplankton, benthos, and fish. Based on the information generated by these studies through 1978, NRC determined that Sales had no impact on phytoplankton and microzooplankton populations due to their high abun-dance and short generation period. NRC also determined that benthic invertebrates had relatively little interaction with Salem station and therefore also would not be affected by station operation. Accordingly, NRC amended the ETS in 1978, daleting further study of these assem-blages. .This permitted PSE&G to concentrate on the assemblages with greater potential for impact: macrozooplankt.on and fishes (NRC 1979a, 1979b, 1983). During summer 1978, a period of exceptional juvenile weakfish abundance o throughout the Delaware system, unusually high weakfish impingement
\ rates were measured at Salem. Although such rates were unprecedented and have not recurred, Salem's fish-return systems have been since l 4.1-1 I
Salem 316(b) Dem:nstrction modified to reduce impingement mortality (Section 3.3.1.1). This event relatively early in the history of operacional monitoring focused public and regulatory attention on the potential for impact to fish species. In response, representatives of PSE&G and IA met on several occasions in July and August 1978 with representatives of the U.S. Environmental Protection Agency-Region II (EPA), the New Jersey Department of Envi-ronmental Protection, the Delaware Department of Natural Resources and Environmental Control, the U.S. Fish and Wildlife Service (FWS), the National Marine Fisheries Service, the Nuclear Regulatory Commission, and the Delaware River Basin Commission. The objective of these meet-ings was to bring together personnel who were familiar with the Delaware system and its aquatic life and knowledgeable about available informa-tion and data-gathering techniques. This group discussed and eventually egreed upon a method for studying the environmental ef fects of the Salem cooling water intakes on the Delaware River. Representatives of these agencies were subsequently appointed by EPA to a Technical Advisory Group (TAG), which reviewed the Salem 316(b) project status and provided guidance for the Plan-of-Study (POS). At one such meeting in Middletown, Delaware, representat1ves of PSE&G, IA, and TAG developed a list of key, or " target," species that were to become the subject of the Demonstration. Based on the participants' prior experience with the Delaware system and the aquatic life inhabit-ing it, and on studies performed by and for PSE6G from 1963 through 1978, eleven target species were agreed upon. EPA formally approved these target species as part of the original POS (Beck 1979). The list included the nine fishes and two macroinvertebrates discussed below. h Detailed information about each target species can be found in Appen-dixes II through III. 4.1.2 SELECTED 'iARGET SPECIES 4.1.2.1 Veakfish (Cynoscion,yegalis) This sciaenid species is an anadromous species that lives in the ocean and spawns in estuaries, including the Delaware estuary. Adult weakfish spawn in Delaware Bay in later spring and summer, and larvae and young are soon6 transported throughout the Bay and into the Artificial Island area, which they use until the end of summer as part of the larger Delaware nursery area. Weakfish, an important component of both the commercial, and sport fishery, is an appropriate target species because of its economic importance, its seasonal involvement with Salem station, and its role as a major predator in the River. 4.1.2.2 Bay Anchovy (Anchoa mitchilli) Bay anchovy is the most abundant marine and brackish water forage A species in the Delaware estuary. All life stages occur in abundance throughout the estuary as well as in the vicinity of Salem. Although some spawning occurs in the Artificial Island area, the primary sites for spawning are located farther south. The brackish water portion of Delaware River serves as part of the larger nursery in the Atlantic coastal waters. Anchovy typically occur from April to December, with 4.1-2
Sales 316(b) Demonstration seasonal peaks in production during summer. Although comprising a large biomass,. bay . anchovy is not fished commercially. Throughout its range, however, it is forage for commercially and recreationally importent fishes. A plentiful, small, and short-lived pelagic species, bay anchovy is impinged and entrained in relatively large numbers during all life stages. It also serves an important role in estuarine energy flow. For these reasons, it was selected as a target species. 4.1.2.3 White Perch (Morone americana) A member of the temperate bass family Percichthyidise, the white perch historically has been a semi-anadromous resident of the estuary. It is a schooling species, which occurs in shallow areas of the River during spring and fall. The species overwinters in the Bay and typically is found in the vicinity of Salem from midwinter through early spring. It is both commercially and recreationally important, supporting a Dela-ware Bay winter fishery. White perch eggs and larvae are not subject to substantial entrainment at Salem station because spawning occurs far upriver. The species is, however, abundant at times in impingement samples during midwinter to early spring. l 4.1.2.4 Striped Bass (Morone saxatilis) Otriped bass is an anadromous member of the temperate bass family, found in relatively small numbers in the Delaware River estuary. Although it ' is typically an important member of other mid-Atlantic estuaries, it is O e et7 6 4 e t > 1 =tv r rer e tee 117 stood, but probably related to. destruction of suitable spawning habitat. a t-Striped bass were abundant in the Delaware during the early 1800s, but numbers declined rapidly during the latter portion of that century. Almost all striped bass taksu in the area are from coastal Delaware waters, not from Delawars River. This catch is insignificant relative to the commercial and sport catches from Chesapeake Bay and the coastal ! waters of New York, New Jersey, and New England. Because of their historical importance and the slowly improving water quality within the Delaware Basin, there is some hope that striped bass may return t in abundance to the Delaware system in the future. For these reasons, and because of its role in the Hudson River 316(b) proceedings, striped bass. is an appropriate target species. 4.1.2.5 Blueback Herrina (Alosa aestivalis). Alewife
- (A. oseudoharennus) and American Shad (A. sanidissima)
The family Clupeidae is represented in the Delaware estuary by members of the genus Alosa-the river herrings and shads. Blueback herring, alewife, and American shad occur in abundance in the study area. All three are anadromous with strong schooling behavior and occur in the Artificial Island area during their spring migration to, and fall emi-gration from, upriver fresnwater spawning areas. Although the primary importance of the Salem area to the young of all three species is as a
- O return route to the open sea in fall, some young alewife and blueback may use it as a nursery in spring' and summer. Near Artificial Island, adults of all three species are most abundant during spring spawning 4.1-3
Salem 316(b) Demonstrction runs, although American shad are less abundant than either river her-ring. All three species are recreationally and commercially important throughout most of their ranges, although commercial and recreational g exploitation within the Delaware estuary is generally restricted to ) American shad. American shad has been studied intensively for many l years by FWS and the states of New Jersey and Pennsylvania to determine its population status and to develop management plans. 4.1.2.6 Spot (Leiostomus xanthurus) 1 The spot is a marine member of the drum family Sciaendae and occurs annually in the estuary in the vicinity of Salem from May to December. Spot is different from most other Delaware 4pecies in that it spawns primarily during winter in coastal waters. Young spawned offshore i appear locally during late spring and remain until fall, using the l tidal creeks and marshes, upper Bay, and lower River as a nursery area. 1 During the 1950s, spot were of commercial importance in the Delaware; however, landings have since been small. It was not a dependable fisaery due to sporadic abundance. Presently, there is no commercial spot fishery in the River because its abundance apparently undergoes great yearly fluctuations. Spot also show great impingement and entrainment variability at Salem station, with peaks in abundance typically occurring during summer and fall. 4.1.2.7 Atlantic Crosker (Micropogonias undulatus) Also a member of the drum family, Atlantic croaker occurs annually in the Delaware River estuary. It is common in the study area during fall, g with the influx of young of the year entering the estuary from offshore spawning grounds and leaving the Bay during November and December. Croaker is a relatively short-lived species, with a typical life span of one to four years. There is a small Middle Atlantic commercial and recreational fishery. Catches declined in the 1950s and 1960s, but croaker abundance appears to have increased in the 1970s. Croaker uses the study area as a fall nursery and is then susceptible to impingement l at Salem station. l l 4.1.2.8 Opossum Shrimo (Neomysis americana) The opossum shrimp is the most widespread and abundant marine mysid, preferring water with salinities in excess of 4 ppt along the north-i eastern coast of the United States, including Delaware Bay. It serves an important role in the transfer of energy between estuarine trophic j levels. Feeding on phytoplankton and detritus and probably copepods, it is, in turn, fed upon by other invertebrates and fishes. It appears in the diet of weakfish, Atlantic croaker, and bay anchovy, as well as ! striped bass and white perch. 4.1.2.9 Scud (Gammarus spp.) This taxon in the Delaware River is composed of three species preferring differing salinities-G. fasciatus, G. daiberi, and G. tigrinus-which overlap in distribution in the study area portion of Delaware Bay. g l Cammarus spp. is important in the food web since it is an omnivorous i 4.1-4 l
Salem 316(b) Deurn:tration
. scavenger and an important food source for many fishes. It is included in the diet of weakfish, white perch, and Atlantic croaker.
4.1.3 THE ROLE OF TARGET SPECIES The 11 target species selected for this Demonstration were intended to serve as indicators of the effect of the operation of Salem on the ecological quality of the Delaware River aquatic community. Detailed examination of each of the myriad species present was recognized as unnecessary and unfeasible (EPA 1977). As indicated above, several of the target species were chosen, in part, because of their then current relatively high involvement with Salem station, or their potential for future involvenent. Species with relatively high involvement include bay anchovy, white perch, weakfish, N_. americana, and Gammarus spp. Other species, such as striped bass, the Alosids, spot, and Atlantic croaker, have been either present in large numbers in the Bay in the past or asy be in the future. Several species'also were~ chosen because of their present value or potential future value for human uses of Delaware Bay, White perch, blueback, alewife, shad, croaker, and weakfish are all presently valu-able in either the commercial or recreational fishery. In addition, four of the target species are among those that play an important role in the transfer of energy within the system. Many abundant species are found in the tidal marshes and the littoral / pelagic zones of the Delaware system. The ecological and trophic func-tions of these nontarget species are represented by target species with similar functions. Thus, the target species are not simply a repre-sentative cross section of species commonly found in the Bay. Rather, they are a set of species selected especially to serve as a sensitive indicator of any effects that might result from the operation of cool-ing water intake systems. They are species with relatively high poten-tial for statfon invoavement, species of particular commercial and recreational value, and species important to the food web and overall ~ ecology of the Delaware system. O 4.1-5
~
Salem 316(b) Dem nstrstica 4.2 THE STUDY OBJECTIVES AND PLAN-OF-STUDY 4.2.1 OBJECTIVES Essentially, the goal of the Salem studies was to determine what effect, if any, the operation of the station's cooling water intake has on the ' ecology of the source waterbody. Accordingly, these studies thus were designed ta develop information on the entrainment and impingement survival rates of target species, and on such relevant aspects of the source populations as population size, distribution, age composition, reproduction, r:ortality, growth rates, and exploitation. By comparing the anticipated losses with the information on the source populations, biologists could arrive at conclusions about the nature and significance of those losses. Biological consultants to PSE&G have developed extensive life history information on esco target species, through both direct field observa-tion and literature reviews. That information is detailed in Appendixes II thrcugh III of this Demonstration and summarized in Section~ 5. They also have collected and analyzed a great deal of information on the overall ecology and functioning of the Delaware system (summarized in , Section 2). Most of the remaining quantitative studies can be divided logically into two types: those aimed at (1) determining the numbers of each target species lost due to impingement and entrainment at Salem, and (2) determining the relevant characteristics of the source popula-tions.. The more immediate objectives of these studies are explained g below. A summary of how they were conducted appears in Sections 4.3 V and 4.4; a complete dascription of study methods appears in Appendix I. 4.2.1.1 Entrainment and Impingement Studies The basic rationale of the entrainment studies was first to estimate the densities at which target species of different age categories are entrained at Salem throughout a " typical" year. Other studies would provide estimates of the rates at which entrained organisms of the various species and life stages survive or succumb to entrainment. From this informe. tion, it would be possible to calculate the rates at which orgauli,ms of each species and age class are lost due to entrain-ment throughout the year (i.e., the number lost per unit volume of cooling water pumped). Multiplying these rates for a particular portion of the year by the volume of cooling water likely to be pumped during that period in a typical year yields the estimated number lost in that interval by species and life stage. The losses associated with all age categories during each interval in the year could then be aggregated to provide an estimate of annual cropping. Two types of studies were performed to estimate entrainmetit densities independently by species and life stage: the Onsite Entrainment Abundance Study and the Ichthyoplankton W-Factor Program. Both of these studies are summarized in Section 4.3.1.1, with citations to more detailed discussion in Appendix I. O O 4.2-1
Salem 316(b) Demonstration Studies were performed which together would allow entrainment survival rates to be determined (Sections 4.3.1.2 and 4.3.1.3). These included & W initial survival, latent mortality, collection-induced mortality, and entrainment-simulation testing designed to determine what stresses associated with entrainment were the most dif ficult for organisms to withstand. In addition, PSE&G's biological consultants have performed entrainment survival studies at other sites and conducted an extensive literature review of studies by other researchers. The impingement studies parallel the entrainment program. The first step was to generate estimates of the densities at which target species of Jifferent age categories are impinged throughout a " typical" year. Other studies would provide estimates of the rates at which impinged organisms of the various species and varying ages survive or succumb to impingement, From this information, it would be possible to calculate the rates at which organisms of each species and age category are lost due to impingement throughout the year (i.e., the number lost per unit volume of cooling water pumped). Multiplying these loss rates for a ' particular portion of the year by the volume of cooling water likely ; to be pumped during that period in a typical year yields the estimated number lost in that interval by species and life stage. The losses associated with all age categories during each interval in the year could then be aggregated to provide an estimate of annual cropping. . To determine impingement densities over the study period by species and age, impingement abundance sampling and "w-factor" sampling was conducted. Summary discussions of these programs appear in Section 3 4.3.2.1 and 4.3.2.2, with citations to a more detailed account in W i Appendix I. Two studies were conducted to determine impingement survival rates: analyses of initial survival and latent mortality (Section 4.3.2.3). As with entrainment survival, PSE&G's biological consultants have per-formed impingement survival studies at other sites, and have conducted an extensive literature review of studies by other researchers. - 4.2.1.2 Population Studies The population studies consisted of sampling programs, laboratory investigations, and literature reviews designed to determine relevant attributes of populations of the target species, including numbers, distribution, age composition, reproduction, mortality, growth rates, feeding habits, and exploitation. Sampling programs were targeted at particular species and life stages (the Ichthyoplankton Field Prorgam described in Section 4.4.2.1, the Macroinverteorate Field Program des-cribed in Section 4.4.2.2, and the Juvenile and Adult Finfish Trawl Program described in Section 4.4.3). They consisted of sampling the study areas through appropriate sampling designs, and recording the . number and lengths (from which age might be inferred) of the organisms recovered. Given enough of this information, population and age dis-tributions could be projected. O r-4.2-2 m um um-m m m
~ __
Salem 316(b) Demsnstration A fourth study, the White Perch Mark-Recapture Progren, was designed specifically to decemmine the distribution and size of the 0+ white O perch population in the study area (detailed in Section 4.4.4). It involved capturing, marking, and releasing a large number of 0+ white perch in the Delaware River, and then noting the number of marked versus unmarked 0+ white perch recovered later in samples taken in the study area. From this information, estimates of the Delaware River white perch population can be calculated.
, In addition, a laboratory study of larval and juvenile fish age and l'
associated growth rates was performed to determine the periods of cer-tain species' susceptability to entrainment or impingement (Section 4.4.5), and additional field studies examined hydrodynamics in the vicinity of Salem's cooling water intake (Section 4.4.6). 4.2.2 THE PLAN-0F-STUDY Many regulatory agencies--known collectively as the Technical Advisory Group--participated in formulating the Salem 316(b) Plan-of-Study. Their involvement helped ensure that the study design, data collection methodologies, and procedures were adequate to meet program objectives. EPA formed TAG to assist with review of the 316(b) studies performed by PSE&G and its consultants. TAG's activities were directed by EPA's Water Resources Section. It included representatives from the National Marine Fisheries Service (Office of Marine Mammals and Endangered Species, and the Northeast Fisheries Center); Delaware River Basin O. Commission (Environmental Unit); U.S. Nuclear Regulatory Commission (Siting and Environmental Branch); U.S. Fish and Wildlife Service (Division of Ecological Services, and Bureau of Sport Fisheries (Delaware Fisheries Study]); Delaware Department of Natural Resources and Environmental Control (Division of Fish and Wildlife); and New Jersey Department of Environmental Protection (Division of Water Resources). Typically, TAG met quarterly with PSE&G at EPA's direction. There were a total of 12 meetings: the first held on July 17, 1979, and the last on June 9, 1982. TAG members were provided copies of all 316(b) reports and all correspondence from PSE&G to EPA. At these quarterly meetings, TAG representatives commented on PSE&G's reports and other materials. During approval of the POS, TAG considered a large amount of information developed previously on the nature of Salem's environs (Section 2), and the station's design and operation (Section 3). The POS structured the development of further information on each target species' population aspects (Appendixes II through III), as well as impingement and entrain-ment abundance and survival rate information (Section 6). 4.2.2.1 Oriminal Plan-of-Study Formulation of the POS was based on site-specific knowledge accumulated between 1968 and 1978. Data-collection activities during this period were based on the requirements of the Salen Generating Station Operating (-)/ s, - Licenses DPR-70 and DPR-75 (Appendix B, Environmental Technical Speci-fications and conditions of the Salem Construction Permit. 4.2-3
Salem 316(b) Dem:nstrction The original POS (submitted October 16, 1978, and revised December 12, 1978) considerably expanded the intensity and scope of the ETS data- g collection program. The transient behavior and widespread use of the W estuery by the target species necessitated sampling in a larger area. The POS called for the development of baywida distribution and abundance data, as well as data on induced cropping. Even so, the POS study area was still a compromise. Most target species utilize areas beyond the study area, in the ocean and in the less-saline portions of the estuary. Modifications to this proposed POS, suggested during winter 1978-1979, were supported by a series of special studies. EPA gave formal approval on May 25, 1979, af ter soliciting and receiving comments from TAG. The original POS defined a study area which encompassed the entire Delaware Bay and part of the lower Delaware River. The ETS program encompassed a much smaller area in the vicinity of Salem (rkm 64-96); Salem is at rka 80. Baywide field studies employed trawls for postlarval fish, and plankton nets for ichthyoplankton and macroinvertebrates. Sampling locations were selected based on a simple random-selection design. On-station impingement and entrainment studies continued to use methodologies similar to those utilized in the ETS. 4.2.2.2 "Second Year" Plan-of-Study Approximately one year after approval of the original POS, PSE&G pro-posed and implemented for 1980 several modifications such as stratified g random sampling to improve the accuracy of information obtained through W the population studies and the entrainment sampling program. Population characteristics were to have been evaluated on the basis of a baywide multispecies program. However, since species were found to have exhib-ited very different temporal and spatial distributions, abundances, and associated sampling gear bias, further modifications to the program were required. The goal of the origins 1 sampling program was to address evenly all tar-get species. In attempting this, the data proved marginal for weakfish and bay anchovy and insufficient for others. In addition. -atrainment estimates were proving to be highly variable due to small sample size (i.e., number of organisms per sample) and variable station operations which affected (and, at times, inhibited) the collection of entrainment samples. 4.2.2.3 Final Plan-of-Study In mid-1980, TAG members proposed a mathematical biological modeling approach as a method for quantifying impact. Since models examining community-level effects required a wide variety of data not reasonably obtainable, TAG undertook to examine suitable models for quantifying population-level effects. It was also obvious that complete model data could not be obtained reasonably for all species. After a series of discussions, PSE&G and TAG agreed that mathematical models should g be proposed for white perch, weakfish, and bay anchovy (then called w " primary" target species) and that modeling would not be required for 4.2-4
Salem 316(b) Den:nstration spot, Atlantic croaker, Neomysis americana, Gammarus spg. , American shad, blueback herring, alewife, and striped bass (the secondary" p/ L target species). However, e data set, as complete as reasonably possible, would be collected. i PSE&G and IA prepared two modeling workshops for EPA and TAG to present the various attributes of the available models. Modeling was also discussed at several TAG meetings. 'In this way, TAG participated in the model-selection process. ; EPA approved this final POS on March 18, 1981, and this was pursued through the end of the collections. Data-collection activities were concentrated on the primary target species to develop information needed for model inputs. Further, entrainment samples were collected more frequently (using a high-volume sampling device) and on a schedule emphasizing the primary target species. I 4 O l l l l l l O 4.2-5
Salem 316(b) Dem:nstration 4.3 ENTRAINMENT AND INPINGEMENT ABUNDANCE AND SURVIVAL STUDIES 4.3.1 ENTRAINMENT 4.3.1.1 Entrainment Abundance _0ggite Studies To determine the number and species of organisms entrained at the Salem cooling water system (CWS) intake, PSE&G and its consultants designed and conducted a study program involving an extensive sampling ef fort over a period of five years. During the period August 1977 through l- April 1978, samples were collected monthly from September through May and twice monthly from June through August. In 1979, the sampling schedule was altered to focus on periods of peak involvement. Samples were collected one day per month in March, April, October, and November; two days in May, August, and September; and four days in June and July. Replicate samples were taken every four hours during a 24-hour period until May 1980. The sampling program was further concentrated during the period of maximum ichthyoplankton abundance during 1980. Four samples were-taken during a 24-hour period on every fourth day from May through October, to emphasize target species. Sampling continued in this fashion during 1981 and 1982 (Appendix I, Section 5.1.1.2). A total of 437 entrainment abundance samples were processed for macro-zooplankton (1977-1980); 771 were processed for ichthyoplankton (1977-1982). Annual numbers of ascrozooplankton samples were 23 in 1977, 0 132 in 1978,100 in 1979, and 182 in 1980. Annual numbers of ichthyo-plankton samples were 24 in 1977,135 in 1978, 92 in 1979,195 in 1980, 143 in 1981, and 182 in 1982. Sampling dates, number of samples, and volumes filtered are listed in Tables 5.1-1 and 5.1-2 of Appendix 1. During the period August 1977 through May 1980, samples were collected exclusively from CWS intake bay 11L or 12E (Figure 4.3-1), except during a plant outage in 1979, when samples were taken in front of the trash racks at forebay 21A. (the only circulator in operation during the col-1ection period). These intake samples were taken at a noint inboard of the vertical traveling screens and upstream of the circulating water pumps (Appendix I, Figure 5.1-5). After an evaluation of the suita-bility of discharge sampling during June 1980 (Appendix I, " Sampling Locations" Section 5.1.1.1), the discharge standpipes were adopted as
.the primary sampling location. Discharge water was withdrawn through a 15.2-cm (6-ic.) PVC tube inserted through the standpipe to the discharge pipe. After June 1980 the intake locations were used only if mechanical difficulties or station operating conditions precluded discharge sampling.
Samples were taken by pumping water with a Nielsen fish pump through a plankton net and abundance chamber. Af ter diverting flow, the plankton not was removed from the chamber and the sample contents were rinsed into a jar and preserved with formalin Rose Bengal solution. Equipment i and collection procedures are described in detail in Sections 5.1.1.2 and 5.1.2.2 of Appendix I. 4.3-1
i Salem 316(b) Dem strctica In the laboratory, samples were washed to remove formalin. Fish eggs were counted and examined to determine viability. Larval, juvenile, and adult fishes were counted and measured to the nearest 0.5 mm TL; g macroinvertebrates to the nearest 1 mm TL. Records were maintained of species present, the number of each, and the length of each specimen (from which age can be estimated). Data reduction and statistical procedures are discussed in detail in Section 2.4 of Appendix I. Ichthyoplankton W-Factor Program The Ichthyoplankton W-Factor Program was conducted during June through August 1981 and 1982 to develop model inputs for bay anchovy and weak-fish. Samples were collected adjacent to the intake structure, in five offshore horizontal strata (Appendix I, Figure 4.4-3). Detailed sam-pling procedures are contained in Section 5.3.3 of Appendix I. These data ultimately are combined with onsite entrainment estimates to improve the entrainment estimates. During 1981,'20 samples (5 inshore-offshore pairs during total darkness and 5 during daylight) were collected during each sampling period for a total " seasonal sample" of 160 (Appendix I, Table 5.3-1). Samples were taken from June 3 through August 5 during eight periods--four in June, three in July, and one in August. Samples were collected as five pairs, each consisting of a discrete inshore sample frem immediately in front of the intake and an offshore sample from one of the five horizontal strata (Appendix I, Figure 4.4-3). In 1982, 38 samples were collected on each sampling date for a total h
" seasonal sample" of 264 (Appendix I, Table 5.3-2). Samples were taken during seven periods (3 in June, 3 in July, and 1 in August) from June 8 through August 4. Two vertical strata were established in all zones except WOO 5 (Appendix I, Figure 4.4-3), where water depth was <3 m.
All samples in the W-Factor Program were collected with the metered 0.5-m (0.5-mm mesh) conical plankton net. During 1981,.a single oblique tow run stepwise from surf ace to near bottom ves used. In 1982 sampling consisted of two stepwise (1.5-m intervals), oblique tows done simulta-neously--the first from near-surf ace to middepth and the second from middepth to bottom. Refer to Section 5.3.3.2 of Appendix I for detailed collection procedures. 4.3.1.2 Entrainment Survival Many entrained organisms survive passage through the CWS. To determine the survival rate of entrained organisms at Salem station, studies were conducted from 1977 through 1982. A sampling program was conducted to determine the percentage of each species that complete the entrainment process alive. Since some of the live organisms may have been injured, samples were held for various periods to determine the extent of any latent mortality. Further, since some of the mortality in these samples results from the stresses of the sampling and holding methodology itself, control groups were used to determine collection-induced mortal- 3 ity. These programs are summarized below and are explained fully in T Appendix I. 4.3-2
Salem 316(b) Dem:cstration Survival To determine the survival rates of organisms entrained at Salem station, a sampling program was conducted from 1977 through 1982. Due to plant outages, few samples were collected in 1977 (2 experiences, 15 samples), 1978 (3 experiences, 48 samples), and 1979 (no samples). In 1980, sampling began _ in April and continued through October (10 experiences , 204 samples). During 1981 and 1982, the sampling schedule was intensified to include sampling experiences four times monthly in June and July, twice monthly in May and August, and once each in September and October. Sampling was conducted in 1981 from May through October (11 experiences,170 samples) and in 1982 from June through September (12 experiences; 197 samples). A summary is presented in Table 5.1-6 of Appendix I. Sampling locations for entrainment survival were the same as for entrainment abundance (Figure 4.3-1). Intake and discharge locations were sampled using duplicate collection gear to equalize gear-induced mortality. From 1977 through 1980, entrainment samples were collected using a centrifugal fish-transfer pump and a one-screen larval table. Samples were collected using the low velocity fiume (LVF) in 1981 and 1982 to provide a larger sample size. The LVF, a modification of the larval table, permits sampling of a larger volume of water without increasing sampling mortality. Detailed descriptions of the equipment are presented in Section 5.1.2.2 of Appendix I. Discharge samples were taken several minutes af ter the intake samples, depending on which forebays and discharge standpipes were used. The delay corresponded to plant transit time and allowed the intake and discharge samples to be taken from the same " block" of entrained water. Detailed collection procedures are provided in Section 5.1.2.2 of Appendix I. Af ter larval table or LVF sampling, specimens were taken immediately to the onsite laboratory to determine their condition. Researchers examined the specimens and ree.orded the number and condition of each organism of each species. Specimens were classified as " live,"
" stunned," or " dead" according to established criteria. Live and stunned specimens were held for latent mortality studies. Details of specimen transfer and sample processing are given in Section 5.1.2.2 of Appendix I.
During 1977 and 1978, the latent-mortality holding period was 12 hours. In 1979 and 1980, the specified holding period was increased from 12 to 24 hours for bay anchovy. According to the approved EPA POS Modifi-cation (March 18, 1981), holding times on selected species were further extended to 96 hours for white perch and weakfish. During -the shorter holding periods in 1977 and 1978, specimens were not fed. As holding periods were extetided in 1979 through 1982, feeding p became necessary. Specimens were typically fed appropriate food twice V daily (Appendix I, Section 5.1.2.2, " Sampling Processing"). 4.3-3
Salen 316(b) Dem:nstrctica Collection-Induced Mortality Tests were conducted from 1979 through 1981 to determine the extent of collection-induced mortality. A total of 5,173 larval and juvenile fishes of five taxa, 6,069 N. americana, and 371 Cammarus spp. were tested to determine collection- and holding-induced mortality. These tests included 1,599 control fish, 850 introduced directly into the larval table (table-only), 944 introduced into the LVF (LVF-only), and 1,780 that passed through the fish pump and into the larval table (pump / table). The fish species tested were alewife, blueback herring, white perch, weakfish, and spot. Collection-induced mortality is divided into components of mortality due to holding, larval-table passage, low-velocity fiume passage, and fish-pump passage. Refer to Section 5.1.2.2 (" Sampling Equipment") of Appendix I for results of the tests for each species. 4.3 .1.3 Entrainment Simulation 5 Simulated entrainment studies were conducted in an effort to quantify the knows stresses associated with entrainment that cause organism mortality. From 1974 to 1982, test organisms were subjected to varying pressure and delta-temperature profiles. Each pressure change simulated conditions at a location in the CWS and each delta temperature simulated the range of thermal changes that an entrained organism could experience depending on plant operation. Entrainment simulation tests conducted from 1974 to 1981 included seven treatments: a control, handling control, experimental pressure, two experimental temperatures, and two experimental temperature / pressure treatments. Test treatments in 1982 were modified to include three different transit time profiles. Tests were performed on invertebrates, eggs, prolarvae, early postlarvae, late postlarvae, and young fish. Refer to Section 5.1.3 of Appendix I for details. In 1978, extraction-pressure simuistion studies were added to the pro-gram to examine effects of decompression on the functioning of specimens rapidly removed from the river bottom into the circulating pump housing. The extraction pressure / time profile comprised two phases--the acclima-tion compression regime and the decompression regime. 4.3.2 IMPINGEMENT 4.3.2.1 Impingement Abundance Onsite Studies To determine the number and species of organisms impinged at the Salem cooling water system and service water system (SWS) intakes, a study program was designed and conducted involving an intensive sampling effort over a period of five years. During the period May 1977 through September 1978, CWS abundance samples were collected a minimum of four times per day at 6-hour intervals three days per week. After September g 1978, sampling frequency was increased to a minimum of 10 samples per 4.3-4
Scism 316(b) Dem:nstrctica day six days per week. Based on computer simulation modeling in spring 1980, the impingement abundance sampling schedule again was altered to O permit the collection of a minimum of four samples per day when entrain-ment samples were collected, but sampling continued six days per week. Table 5.2-1 of Appendix I shows the number of impingement samples col-1ected by month and year. More than 16,000 CWS impingement abundance samples were collected between May 2, 1977, and December 31, 1982. Samples were collected in fish counting pools located adjacent to the discharge troughs at the northern and southern ends of the CWS intake structure (Figure 4.3-2). Screen-wash water was diverted into the counting pools from the dis-charge trough. Sample duration was typically three minutes of trough flow, but could vary from 1 to 15 minutes depending on the amount of impinged detritus and the number of screen units in operation. When a sample had been obtained, the pool was drained and organisms were collected with a dip net and placed in buckets. Organisms then were sorted by species, counted, measured, and weighed. Detritus, salinity, and temperature were measured. Refer to Section 5.2.1.2 of Appendix I for details. Impingement collection-efficiency studies were conducted between 1979 and February 1982 to determine the percentage of different size classes of fish impinged on the CWS traveling screens that were not recovered during the spraywashing and fish-collection procedures. These studies were conducted with blueback herring, bay anchovy, white perch, weak-fish, spot, and Atlantic croaker. A total of 134 collection-efficiency O tests were conducted and the percentage recovery per test ranged from 19 to 100 (Appendix I, Section 5.2.1.2, " Sampling Equipment"). A total of 678 SWS abundance samples were collected between April 18, 1977, and September 20, 1979 (Appendix I, Table 5.2-3). Organisms and debris impinged on the SWS traveling screens were front-washed by a high-pressure rpray into a single trough and sluiced to the collection baskets for sampling. SWS abundance samples were either 12 or 24 hours in duration, depending on detrital loading; three samples were taken per week. Organisms were separated from the detritus, sorted by species, counted, and weighed (Appendix I, Section 5.2.1.2, " Sample Processing"). Vertical Profile Promram
.The Vertical Profile Program was conducted during October through November 1979 and March through October 1980 to determine the relative abundance of organisms in surf ace, middepth, and bottom waters adjacent to Salem and in the baywide study area. Samples were collected adjacent to the intake structure and along two additional downbay transects (Figures 4.3-3 through 4.3-5) . Detailed sampling procedures are pre-seated in Section 5.4 of Appendix I.
During 1979, 17 surf ace, middepth, and bottom samples were collected per sampling period on a transect adjacent to Salem (Figure 4.3-3). The transect included seven horizontal strata and vertical strata at 3-m Oi intervals within each. All strata were sampled during each collection period. 4.3-5
Salem 316(b) Dem:astrctica In 1980, the Vertical Profile Program was expanded regionally to include two vertical profile transects in the downbay area (rkm 13,and rka 37), in addition to the transect adjacent to Salem station. A total of 57 g surf ace, middepth, and bottom trawl samples were scheduled during each baywide vertical profile collection period (Figures 4.3-4 and 4.3-5). During March, May through August, and October, from 17 to 57 vertical profile collections per sampling period were taken (Appendix I, Section 5.4-9). Horizontal and vertical str'ata sampled on each transect were chosen systematically to provide a representative coverage of the rela-tively large bay cross section with the available resources. Vertical profile samples were collected in 1979 and 1980 with the 4.9-m otter trawl. All trawl samples were 10 minutes in duration and taken in the direction of the tide at a standard tow speed of ~3 kt. Trawl samples were taken at predetermined locations designated by either Loran C coordinates or visual landmarks in conjunction with water depth. Refer to Section 5.4.2 of Appendix I for detailed collection and sample processing procedures. W-Factor Program To estimate the abundance of organisms in the power plant intake water relative to their average abundance in an adjacent cross section of the River, a w-factor sampling program was conducted in 1981 and 1982. Samples were collected adjacent to Salem along the same transect used in the Vertical Profile Program. Detailed sampling procedures are con-tained in Section 5.4 of Appendix I. In 1981 and 1982, w-factor sampling was completed weekly during May through October (Appendix I, Tablea 5.4-10 and 5.4-11). Horizontal and vertical strata campled along the Appoquinimink/ Salem station transect were essentially the same as for the 1979 and 1980 Vertical Profile Program, except that the two westernmost horizontal strata were consolidated (Figure 4.3-6). W-factor samples were collected as pairs, each consisting of a surface, midwater, or bottom sample taken near the intake; and another taken in the same offshore vertical strats, but in a randomly selected horizontal strata. Bottom strata were sampled with a 4.9-m otter trawl and the 1.2 x 1.8-m fixed-frame trawl was used for pelagic sampling. Refer to Section 5.4.2 of Appendix I for detailed collection and sample process-ing procedures. 4.3.2.2 Impingement Survival All organisms impinged on the CWS intake are returned to the River, and many survive. To determine the survival rate of impinged organisms, studies were conducted to determine both initial and latent impingement survival . These programs are summarized below and are explained fully in Appendix I. O 4.3-6
Sslem 316(b) Demststrction Initial Survival To determine initial survival rates and physical condition of impinged organisms returned to the River, more than 12,000 initial-survival sam-pies were collected between May 2, 1977, and December 31, 1982. Samples were collected three days per week through October 17, 1978, conditions permitting. After October 17, 1978, if impingement levels for selected target species exceeded predetermined levels for two samples in a 24-hour period, the frequency of sampling was increased to six days per week. Sampling locations and duration for initial-survival sampling were the same as for impingement abundance. Combined fish-trough and trash-trough screen-vash discharges were diverted into a partially filled counting pool, where -the sample was held for five minutes for specimen re-orientation. The water then was drained from the pool and, as the water level dropped, organisms were collected with a dip net and sorted into separate tubs as live, damaged, or dead. Specimens in each of the three condition classes were identified to species and the total number and weight, minimum and maximum length and weight, and length-frequency distribution determined. Latent Survival Some organisms classified as " live" during initial impingement survival studies may succumb af ter return to the River. Other organisms initi-ally classified as " damaged" may completely recover when returned to the s River. Latent impingement survival studies were conducted to quantify the number of such fish initially included in the " live" or " damaged" category. Samples were collected for latent impingement survival tests at least weekly throughout the year in the same CWS fish-collection pools used to sample impingement abundance. From July through November 1978, only fish initially classified as " live" were tested; thereaf ter, " damaged" fish, including those exhibiting a loss of equilibrium, also were evaluated. Until 1980, all target species were tested as available. Thereaf ter, only the primary target species-bay anchovy, white perch, and weakfish-were tested intensively to maximize data yield. All test specimens were placed in aerated tanks and held for a 96-hour observation period. Test tanks were situated at the IA Delaware Experi-mental Laboratory, at Salen station in the fish collection pools, and in the IA onsite trailer. Observations were made continuously for the first 30 minutes following capture, at hourly intervals for the next four hours, and at approximately 24-hour intervals thereaf ter. Control tests usually were conducted concurrently with tests on impinged specimens. Control fish generally were collected by seine, removed from the net with a water-filled scoop, and transported to the test facili-ties to be held in test tanks. O 4.3-7
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Salem 316(b) Demonstration 4.4 FIELD STUDIES 4.4.1 THE STUDY AREA The combined study area for all Salem 316(b) field studies extends from the mouth of the Delaware Bay (rka 0) upriver as far north as the Burlington-Bristol Bridge (rkm 190) (Figure 4.4-1). A description of this area of the Delaware River estuary is contained in Appendix I, Section 4.2 and in Section 2 of this Demonstration. The study area for each s 2mpling program is a subdivision of the com-bined study area. The sampling region and specific locations within it were determined on the basis of (1) historical infocmation on the spa-tial distribution of target species, (2) sampling location and times determined by experimental design, and (3) navigation limitations. The areas sampled in each field study are identified in the individual descriptions of those studies which follow. Field studies were conducted to gather information pertinent to assessing the potential environmental effects of Salem's cooling water intakes. These studies gathered relevant information on population parameters for each of the target species. 4.4.2 ICHTHYOPLANKTON/MACROINVERTEBRATE FIELD PROGPAM An Ichthyoplankton/Macroinvertebrate Field Program was conducted from 1979 through 1982 to estimate the relative density and provide length-O frequency data for nine ichthyoplankters and two epibenthic macro-invertebrates. This information was needed to estimate population size, relative density, or age composition. The field program evolved during the course of study and the program design was modified as necessary to improve sampling efficiency and results. Initially (1979-1980), the study area was divided, based on historical data regarding the distribution of target species, into two regions. The " northern region" (rka 64-117) was sampled from March through mid-May for white perch, striped bass, American shad, the river herrings (blueback herring and alewife), Neomysis americana, and Gammarus spp.; the "baywide region" (rkm 0-117) was sampled from mid-May through November for bay anchovy, weakfish, spot, Atlantic croaker, Gammarus spp., and Ji. americana. In 1981-1982, une program was modified to sample specifically the early life stages of weakfish and bay anchovy from May through November in the baywide re;1c . Other modifications to the program design were related to es*lection procedures, collection frequency, and sampling locations. Details of the field program, modifications, and rationale are contained in Appendix I, Section 5.3; a brief description is included here. 4.4.2.1 Ichthvoulankton Field Program The Ichthyoplankton Field Program was designed to provide relative G density estimates and length-frequency data on early life stages (eggs, larvae, and juveniles) of river herrings (alewife, blueback), 4.4-1
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During 1979-1980, samples were collected monthly in March and April and once during early May in the northern region. Samples were col- 3 lected once or twice during mid-late May, once in November, once or j twice monthly during September and October, twice in August, and three j times each in June and July (Appendix I, Tables 5.3-1 and 5.3-2) in the ._ baywide region to provide data on bay anchovy, weakfish, and Atlantic ; croaker. In 1979, sampling locations were chosen from the grid coordi- -:3 nates (Appendix I, Section 4.1) using a simple random design; however, a j systematic sampling design was adopted in 1980 to minimize extrapolation - and to stabilize among-station variance. During 1979-1980, the sample i size per collection period for ichthyoplankton of the combined nine target fishes ranged from 39 to 79 (Appendix I, Tables 5.3-1 and 5.3-2). During 1981-1982, more intensive sampling of a reduced number of target $ species was conducted. Samples were collected monthly in April and 2 October, twice in September, and three times monthly during May through j August to provide data on bay anchovy and weakfish only. An optimal _ location scheme, in conjunction with a stratified design (Figure 4.4-2), q was used to choose sampling locations from grid coordinates (Appendix I, 2
" Sampling Locations" Section 5.3.1.1). The number of samples per col- 1 lection during 1981-1982 raaged from 64 to 70 (Appendix I, Tables 5.3-3 g ij and 5.3-4) and samples were collected in the entire region, rkm 0-117, w 1 during all sampling periods. ?
Ichthyoplankton samples were collected during daylight with a 0.5-m diameter, 0.5-mm mesh, conical plankton net fitted with a one-pint screened (0.5-mm bolting cloth) plastic catch bucket and a depressor to g ensure proper fishing attitude. Each was taken as a single oblique tow ;g done stepwise at 3-m (10-f t) intervals from near surf ace to near bottom. $ Tows were made at 1.3-1.9 knots in the direction of tidal flow and each j took four to six minutes, not including retrieval time (about 1 minute). h The volume of 'sater filtered was measured with a digital flowmeter sus- i pended slightly off-center in the mouth of the nei.. j R 4.4.2.2 Macroinvertebrate Field Program d The Macroinvertebrate Field Program was designed to provide relative density estimates and length-frequency data on juveniles and adults of Q Gammarus spp. and E. americana coincident with collection of ichthyo- p I plankton data in the rkm 0-117 region of the Delaware estuary. During 1979-1980, samples were collected monthly in March and April and once in early May in the region rka 64-117. Samples were collected once or twice during mid-to-late May, once in November, once or twice monthly during September and October, twice in August, and three times each in June and July (Appendix I, Tables 5.3-8 and 5.3-9) in rkm 0-117. The number of samples per collection period ranged from 39 to 79. g j um 4.4-2 j
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f Sales 316(b) Dem2nstrction Sampling locations were chosen from the grid according to experimental design (Appendix I). Macroinvertebrate samples were collected with the same gear and pro-cedures used for ichthyoplankton (Section 4.4.2.1). A more detailed discussion of collection precedures is given in Appendix T, Section 5.3.2.2. 4.4.3 THE JUVENILE AND ADULT FINFISH TRAWL PROGRAM A final POS baywide trawl program was conducted to gather information on the population parameters of juvenile and adult finfish. Trawl sampling was conducted three times per month during June through September and twice per month in May and October. The baywide study area for trawl sampling was divided into 16 strata based on optimal design for bay anchovy and juvenile weakfish (Figure 4.4-2). Samples were collected from both bottom (bottom 0.627 m) and pelagic water during the trawl program. Eight of the sampling strata were sampled with bottom nets, the other eight with pelagic nets. Seventy sampling stations per program per collection period were allocated optimally by stratum (Appendix I). Bottom hauls were taken with a 4.9-m semiballoon otter trawl. Pelagic sampling was performed with a 1.2 x 1.8-m fixed-frame travi equipped with a flowmeter. Refer to Appendix I, Section 5.4 for details of trawl n deployment and selection of sampling depth. V All juvenile and adult finfish specimens were identified to species, where possible, and enumerated. If more than 500 specimens of a species were contained in a sample, a representative subsample was used to esti-mate the total number. With each collection, a random subsample of 100 specimens of each target species was measured by 5-mm intervals. Target species were blueback herring, alewife, American shad, bay anchovy, weakfish, spot, Atlantic croaker, white perch, and striped bass. All fish except those with deformities or parasites, or those kept for other programs, were returned to the water. Water chemistry measurements were made in conjunction with all collec-tions. Air temperature, water temperature, dissolved oxygen, salinity, and water transparency were recorded. Refer to Appendix I, Section 5.4 for details of collection procedures. 4.4.4 THE WHITE PERCH MARK-RECAPTURE PROGRAM To obtain an accurate and precise estimate of the 0+ white perch popu-lation in the Delaware River, a Mark-Recapture Program was initiated in November 1980. The Petersen Single Census Method and the Schaefer Molhod for Stratified Populations were used to estimate the population size. More detailed discussions of this program are contained in Appendix I, Section 5.5. A brief discussion follows. O 4.4-3 I
Salem 316(b) Demonstrction 4.4.4.1 Mark-Recapture Field Program Marking Phase O To provide an accurate population estimate (95 percent confidence limits within +50 percent of mean) and to meet assumptions of the white perch mark-recapture model, it was estimated that at least 5,000 fish must be marked and 18,000 fish. examined during the recapture phase. To meet this goal, fish sampling and marking was conducted from November 17 through December 18, 1980, October 29 through December 30, 1981, and from November 3 through December 30, 1982. Fish were captured, marked, and released in eight zones from rkm 74 to 190 (Figure 4.4-4) . These zones were approximately 13 rkm long, except Zone 1, which was a small area near Salem, and Zone 8, which extended upriver to include an area where fish congregated in November prior to their downriver migration. Sampling locations within each zone were restricted to a depth of 9 m (<30 ft) to minimize stress related to pressure change and subsequent collection-induced mortality. During the marking phase, white perch were collected using a 4.9-m otter trawl with 5-minute tows at a trawl speed just fast enough to maintain vessel steerage. During f all 1980, only white perch <85 mm FL were fin-clipped. However, aging by scale annuti in 1981 indicated that the break between age 0+ and 1+ fish was closer to 100 mm FL, so fish to this size were fin-clipped in fall 1981 and 1982. Zone-specific fin-clip combinations were used (Appendix I, Section 5.5.1.2). Fish h injured during collection were not marked. Section 5.5.1.2 of Appendix 7 (" Sample Processing") details these methods. Recapture Phase During the recapture phase, white perch were examined daily January 5 through May 18, 1981, January 3 through April 28, 1982, and January 2 through April 21, 1983. Otter trawls and industrial water intake screens were used for recapture; sampling was not necessarily random within a zone. All white perch specimens of less than the monthly length maxima listed below were counced and examined for clipped fins. Scale samples were obtained from fish in the size range overlapping age 0+ and 1+ fish. Af ter aging these fish by scale annuli, the age 1+ fish were subtracted from the total number of examined fish. Predicted Maximum Length Range from Which Month Length (mm FL) Scale Sample Was Reauired January 109 100-109 February 113 104-113 March 117 108-117 April 121 112-121 0 4.4-4
b Salen 316(b) Densnstretion l . After adjusting for mortality resulting from the marking procedure, the- total population of 0+ white perch per zone was estimated. O- Details are given in Section 5.5.1.2 of Appendix I (" Data Reduction") and in Appendix III. 4.4.4.2 ]hyk Evaluation Laboratory Studies I Nkrk Mortality Studies Studies to determine marking-induced mortality were conducted in the laboratory in' order to permit adjustment of the initial number of marked fish to reflect only those actually available to the recapture phase of the field program. The experimental design was to hold test (marked) and control (unmarked) specimens at several representative temperature / salinity combinations for observation. Any difference in mortality between the marked and unmarked fish then could be determined (Appendix I, Section 5.5.2.1, " Experimental Design"). Mark Retention Studies Mark Retention Studies were conducted to determine the rate of fin regeneration and the duration of positive mark recognition. Specimens held in the mark mortality studies were used to evaluate fin regenera-tion. Each mark type was represented equally in the 1980-1981 test population, but since no fin-regeneration occurred, equal representation of marks was not required in the 1981-1982 or 1982-1983 studies.
, () Initially, 5-10 fish of each mark were observed twice per month, but observations were reduced to once per month since marks remained intact.
1 To minimize stress, fish were not removed from the water during these i observations. Marked fish that died were examined carefully with a dis-section microscope to determine if any regeneration had begun. Upon termination of the holding period, all marked fish were examined closely and a random sample of each type mark preserved for the record. Refer to Section 5.5.2.2 of Appendix I (" Execution") for more information. 4.4.5 AGE-AND-GROWTH STUDIES OF LARVAL AND JUVENILE FISH Age-and-growth studies were conducted with larval and juvenile bay anchovy and weakfish, as a basis for growth curves needed to determine the periods of susceptability to entrainment and/or impingement at Salem for these species. However, all attempts to rear bay anchovy were unsuccessful, and low success in collecting weakfish eggs in 1982 resulted in the production of only one cohort of specimens for study (Appendix I, Section 5.6). A total of 113 measurements of weakfish larvae and juveniles were taken between July 8 and September 20. Beginning at the age of 6 days, 10 randomly selected weakfish were measured on a weekly basis. Later in the study, the remaining specimens, which had reached juvenile propor-tions and were resistant to handling mortality, were returned to the s trough to extend the duration of the study. The study was terminated
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Salem 316(b) Dem:natration 4.4.6 OTHER FIELD STUDIES Various other field studies were conducted for PSE&G as part of the Salem 316(b) studies. These field studies include:
- 1. Intake Velocity Study Circulating and Service Water System Salem Generatire Station
- 2. Net Transport Study in the Vicinity of the Salem Generating Station
- 3. Near-Field and Far-Field Current Velocity and Circulation studies in the vicinity of the Salem Generating Station
- 4. Circulating Water System Dye Recirculation Study Salen Generating Station O
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Salen 316(b) Demonstration LITERATURE CITED: SECTION 4 Reck, E.C. 1979. Letter to J.A. Shissias approving Salem 316(b) Plan-of-Study. May 25. Nuclear Regulatory Commission (NRC). 1979a. Amendment 19--Salem Nuclear Generating Station, Environmental Technical Specifications, Unit 1. Appendix B Operating License DPR-70, October 12, 1979. Nuclear Regulatory Commission (NRC). 1979b. Amendment 23-Salem Nuclear Generating Station, Environmental Technical Specifications, Unit 1. Appendix B Operating License DPR-70, December 13, 1979. Nuclear Regulatory Commission (NRC). 1983. Amendment 51-Salem Nuclear Generating Station, Environmental Technical Specifications, Unit 1. Appendix B Operating License DPR-70. March 11, 1983. Public Service Electric and Gas Company' (PSE&G). 1971. Salem Nuclear Generating Station Environmental Report--Operating License Stage. Newark, N.J. U.S. Environmental Protection Agency (EPA). 1977. Guidance fse Evaluating the Adverse Impact of Cooling Water Intake Structures on the Aquatic Environment: Section 316(b). PL92-500. Office of Water () Enforcement. Washington, D.C. 9 0
Salem 316(b) Demonstration l O SECTION 5: LIFE HISTORY SUMMARIES FOR THE STUDIED SPECIES fD v O
c Salem 316(b) Dem::nstration SECTION 5: LIFE-HISTORY SUMMARIES FOR THE STUDIED SPECIES Page LIST OF FIGURES 5.1 THE MACR 0 INVERTEBRATES 5.1-1 5.1.1 Neomysis americana 5.1-1 5.1.2 The Gammarus tigrinus Group 5.1-2 5.2 THE FISH 5.2-1 5.2.1 Alewife 5.2-1 5.2.2 Bay Anchovy 5.2-2 5.2.3 Blueback Herring 5.2-3 5.2.4 Atlantic Croaker 5.2-4 5.2.5 American Shad 5.2-6 5.2.6 Spot 5.2-7 5.2.7 Striped Bass 5.2-9 5.2.8 Weakfish 5.2-11 5.2.9 White Perch 5.2-12 LITERATURE CITED nV
Salem 316(b) Demonstration LIST OF FIGURES: SECTION 5 Number Title 5.1-1 Range of Neomysis americana. 5.1-2 Seasonal distribution of Neomysis americana in the Delaware estuary. 5.1-3 Range of Gasparus fasciatus. 5.1-4 Range of Gammarus tiarinus. 5.1-5_ Range of Gammarus daiberi. 5.1-6 Seasonal distribution of Gammarus spp. in the Delaware estuary. 5.2-1 Range of alewife. 5.2-2 Spawning areas and seasonal distribution of alewife in the Delaware estuary. 5.2-3 Range of bay anchovy. 5.2-4 Principal spawning area and seasonal distribution of bay anchovy in the Delaware estuary. 5.2-5 Range of blueback herring. 5.2-6 Spawning areas and seasonal distribut. ion of blueback herring in the Delaware estuary. 5.2-7 Range of Atlantic croaker. 5.2-8 - Seasonal distribution of the ocean-spawning Atlantic croaker in the Delaware estuary. 5.2-9 Range of American shad. 5.2-10 Spawning area and seasonal distribution of American shad in the Delaware estuary. 5.2-11 Range of spot. 5.2-12 seasonal distribution of the ocean-spawning spot in the Delaware estuary. 5.2-13 Range of striped bass. 5.2-14 Distribution of striped bass in the Delaware estuary. 9
Salem 316(b) Demonstration . Number Title 5.2-15 Range of weakfish. G 5.2-16 Principal spawning area and seasonal distribution of weakfish in the Delaware estuary. 5.2-17 Range of white perch. 5.2-18 Spawning areas and distribution of white perch in the Delaware estuary. O 1 0
Salen 316(b) Demonstration SECTION 5: LIFE-HISTORY SUMMARIES FOR THE STUDIED SPECIES 5.1 THE MACR 0 INVERTEBRATES 5.1.1 Neomysis americana The mysid shrimp, Neomysis americana (Appendix II), is one of the macro-invertebrate zooplankters that function collectively as an important trophic link in the estuaries and nearshore ocean along the eastern United States from the St. Lawrence River to Florida (Figure 5.1-1). Typically, it occurs at depths of <60 m; offshore, it has been reported at 214 m (Wigley 1964) . Estuaries usually have resident populations (Allen 1978), but there is evidence of seasonal movement between the estuaries and adjacent coastal waters (Hulburt 1957; Allen 1978). The population strategy of N. americans is approximately annual, involving multiple generations of one long-lived, overwintering (OW) generation and, depending upon geographic location (or ambient water temperature), one or two short-lived sumer/ fall (S/F) generations. Apparently, two S/F generations are produced annually in the Delaware estuary. The upper limit of 1. americana distribution in the Delaware estuary seems strongly related to the location of the 4-ppt isohaline (Hulburt 1957) and, therefore, varies seasonally with changes in freshwater run-off and the salinity regime (Figure 5.1-2). During summer and fall, N.- americans occur primarily throughout the deep waters of the estuary
- s to as far upriver as rka 117 (near the Delaware Memorial Bridge), with the greatest concentrations in the mid-to-upper Bay / lower River region and of ten along, the southeastern margin of the lower Bay. During the warm months, the population is maintained largely by in-estuary repro-duction (Hulburt 1957). During winter and spring, based on evidence given in Hulburt, the upper limit of distribution is farther down-estuary (near rka 80), which is near Artificial Island, and the popula-tion is apparently concentrated in deep waters of the lower-to-mid Bay region. Immigration into the lower estuary from adjacent coastal waters may occur during fall and winter (Hulburt 1957; Cronin et al.1%2).
Population maintenance within preferred regions of its seasonal range seems directly related to the species' utilization of the two-layered estuarine transport system. This system comprises the interaction of tidal flow dynamics and vertical stratification by salinity, resulting in a surface current of fresher water moving in a net-downstream direc-tion over a more saline, net-upstream moving bottom current. The organ-isms' preference for darker (photonegative) bottom water, which is more saline, ensures a general upstream movement (Hulburt 1957). At night, some individuals move enough above bottom to enter the net-downstream moving surf ace waters. The two-layered circulation pattern extends farther up-estuary during fall-than during spring, a pattern also evi-dent in the observed seasonal distribution patterns of N. americana. Little or no reproductive recruitment occurs at temperatures below O' about 4.00C; most reproduction in the Delaware estuary occurs during May through November. Egg and larval development occurs in the brood 5.1-1
Salem 316(b) Dem:n trcticn pouch (marsupium) of the female at a temperature-dependent rate; the literature describes total in-marsupium time as about 13 days at 160C and about 24 days at 1000. g Areas of spawning within the Bay are shown in Figure 5.1-1. Spawning also occurs in adjacent nearby coastal waters. Adults spawning during the spring are of the overwintering generation and have survived since summer or fall of the previous year. Their maximum life span is ~ reported as 10-14 months. The individuals are relatively large (2 = 13 mm) compared to summer-generation spawners and, because fecundity is related to size, the number of eggs per spawn (about 60) is also relatively large. Overwintering adults reportedly spawn from one to three times. Calculated in-marsupium mortality for OW-generation progeny, which actually comprise the first summer generation, is esti-mated at 17.5 percent. , Summer / fall individuals are characterized by short life duration; maxi-mum reported life span is 6-10 months. Growth is rapid and maturation is early during the summer months. Maximum growth rate is about 0.09 mm/ day, reached at 250C, and individuals grow to maturity in approxi-mately 45 days. These individuals spawn at a smaller size than OW individuals; therefore, individual fecundity is lower, about 12 eggs. Brood mortality is estimated at 12.8 percent. The rapid growth to maturity characteristic of S/F individuals allows for production of multiple generations and broods, and therefore great reproductive potential. Studies on macroinvertebrates with population strategies simuar to E. americana suggest that this organism can respond to environmental stress (Clutter and Theilacker 1971) by reduction in time to maturity and an increase in individual survivorship and fecundity such that popu-lation growth (r) will increase dramatically (Doyle and Hunte 1981), thereby maintaining the population. 5.1.2 THE Gammarus tigrinus GROUP The Gammarus tigrinus group (Appendix IV) is a species-complex of three morphologically similar species: _G_. tigrinun , G. daiberi, and G. fasciatus, which together with similar macroinvertebrates function as an important link in energy transfer between trophic levels. These three species occur with overlapping distributions in the middle and upper reaches of the Delaware estuary throughout the year, and the complex is represented over a salinity gradient from 1 to 25 ppt. Gammarus fasciatus occurs mainly in fresh water but is found to salin-ities of 3 ppt. It is distributed widely in the eastern United States, ranging from the upper Mississippi River drainage castward through the Great Lakes area and St. Lawrence River System to tide water (Figure 5.1-3). Gammarus tigrinus, the most euryhaline of the three, occurs commonly between 1 and 25 ppt, and ranges from southern Labrador and the northern shore of the Gulf of St. Lawrence south to Chesapeake Bay and, sporadically, south to Florida (Figure 5.1-4) . Gammarus daiberi occurs mainly at salinities of 1-5 ppt, but is sometimes found to about 15 ppt. It is known to range from the Delaware and Chesapeake estuary systens g southward to the estuaries of South Carolina (Figure 5.1-5). 5.1-2
Salen 316(b) Densnstration
.The population strategy of these species is annual, consisting of one long-lived (maximum of about 365 days) overwintering generation and pd several shorter-lived (about 60 days) S/F generations. These S/F generations are characterized by the production of multiple broods per female, the actual number varying with water temperature, which affects the length of the reproduction season.
The composite range of the three spe~cies in the Delaware estuary is approximately from rka 45 to 117 (Cronin et al. 1962); however, the population center seems to shift in response to tidal flow and fresh-water discharge (Figure 5.1-6). Maximum species mixing seems to occur at salinities of 1-3 ppt. During winter and spring, when freshwater discharge is greatest, most animals occur downstream of rka 97. During summer and fall, with decrease in freshwater discharge and concomitant intrusion of saltwater up-estuary, the greatest concentrations occur within the 80-117 (salinity 2-12 ppt). In addition to the main body of the G. tiarinus group located within the lower River / middle Bay region, a few individuals occur occasionally along the margins of the lower estuary, apparently as a result of flushing from the downbay tidal tributaries. These individuals seem restricted to the general vicinity of these tributaries and probably contribute little to the main population. Reproduction within the Delaware estuary occurs mainly during April through November at water temperatures above 6.00C. There may be as many as five generations produced annually. Although some egg-bearing females occur during winter at temperatures as low as 2.500, the low-O or non-occurrence of newly released juveniles in samples during this period indicates little recruitment to the population. Egg and early juvenile development occurs in the female's brood pouch (marsupium) at a temperature-dependent rate, reported only as about 9 days at 210C to 15 days at 130C. In-marsupium mortality is approximately 27 percent. Overwintered adults spawning in the spring have survived since approxi-mately fall of the previous year. These individuals are large (8-12 mm)
-relative to S/F generation spawners, and because fecundity is size-related, the number of eggs is relatively great (about 50) (Section 3.1.7). The CW adults spawn 1-6 times (median of 3) (Hynes 1955) at about 12-day intervals until they die, typically during May-July.
Progeny of the CW generation grow quickly and reach maturity (at 2.4 mm) in about 28 (at 200C) to 41' days (at 1000). Because of their maturation at a relatively small size, fecundity of these S/F spawners is rela-tively ' low: about 17 eggs. However, net production is great due to
- the multiple broods per female during the season.
Studies on another G_ tams _ty_s species evidence an ability to respond to environmental change. Doyle and Hunte (1981) demonstrated that in the absence of density-dependent limiting f actors-a situation maintained by
.the -regular removal of individuals-a population of G. lawrencianus can, within 26 generations (a 3-vear period), compensate for this increased mortality through changes in maturation, s'irvivorship, and fecundity.
O.- It is expected that such compensatory mechanisms would also operate for the Delaware estuary populations of the G. tinrinus group. 5.1-3
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Sales 316(b) Dessustrction 5.2 THE FISH
.5.2.1 ALEWIFE Alewife, A_lgsg oseudoharennus (Appendix V), is an anadromous clupeid found in coastal streams and rivers from North Carolina to Nova Scotia and in a narrow band of coastal ocean waters to a depth of about 146 m (Figure 5.2-1) . It is a pelagic, schooling species. Adults congregate at the mouths of coastal rivers in late winter and early spring prior to upstream spawning runs. In the Delaware system, alewife run at least as far up. ths River as rka 240 at Lambertville, New Jersey, with strays reported as far north as rka 480 near Milanville, New York. Landlocked populations also occur. No clearly discrete stocks have been identified either within the Delaware estuary or in other coastal river systems, although homing to natal streams for spawning has been evidenced.
In the Delaware River and its tributaries, spawning runs begin in March and April and extend through June, typically peaking in early April (Figure 5.2-2) . In North Carolina, spawning runs may begin as early as February; in New England streams, runs are later and may extend through July and August. *dithin the Delaware River estuary, spawning occurs in fresh or slightly brackish waters far up tributary streams from the lower Bay to the fall line and in the tidal Delaware River north of rka 189. Spawning has been reporte.1 at temperatures as low as 10.500 in anadromous alewife, with peak spawning occurring at about 1300. ' f"3 Most alewife on spawning runs are ages 3 through 6, although often age
\_/ 7 and occasionally age 8 or 9 alewife art observed. Age 10 fish have been reported infrequently in North Carolina. Mean length of spawning anadromous adults ranges typically from about 223-246 mm FL (at age 3) through 248-278 mm FL (at age 6), with a maximum size of about 335 mm FL (at age 9).
Fecundity per adult female collected at Lambertville ranged from 128,000 to 288,000 ovarian eggs. Based on other river systems, the reported extremes are 102,800 and 466,701. Egg retention has been estimated to range from 176 to 98,653 eggs; these unspawned eggs are eventually absorbed. Many adults survive their first spawning experience and return to the ocean. Some may spawn again in cubsequent years up to a maximum of six times. Generally, within the Delaware River, 41 per-cent of males and 52 percent of females survived to age 4 or 5, and survival to age 6 or 7 decreased to 33 percent in males and 25 percent in females. Mean survival among 13 areas from North Carolina to Maine, including the Delawars River, was 55 and 56 percent for age 4-5 for males and females, respectively, and 26-33 percent for age 6-7. Alewife eggs, initially adhesive and derersal, are dislodged easily by flowing water and become pelagic. Incubation periods reported for ale-wife range from three days, at 22.20C, to six days, at 15.600. Larvae may be carried short distances downstream after hatching. Laboratory studies indicate that Delaware River larvae are 3-5 mm TL at hatching, have a growth rate of 0.32-0.49 mm/ day, and enter the juveni!- stage O. approximately 35 days after hatching. A wider range of daily growth-rate estimates (0.197-0.908 mm/ day) was reported for field-collected 5.2-1
Salem 316(b) Demonstratior larvae in New England. Mortality rates have not been determined for alewife eggs and larvae in the Delaware River. However, total mortal-ity through life stage in New England has been estimated at 59.5-60.0 g percent for eggs and 75.0-99.9 percent for larvae. Mortality from egg through juvenile emigration in fall was reported as 99.9987 percent. Juveniles begin to leave the upper tidal Delaware River when water temperature declines in September an'd October. They pass through the
-Artificial Island region (rkm 82) primarily from late October through early December and enter the lower Bay by mid-December. During the fall emigration they are approximately 87-93 mm FL. Unusually heavy rains may flush recently transformed juveniles from tributary streams into the lower River and Bay in spring or summer before typical emigra-tion would have occurred. .Some juveniles overvinter in Delaware Bay, others migrate offshore. During winter and early spring, some juveniles may move back upriver to and beyond the Artificial Island area.
There is no local fishery specifies 11y for alewife. An unmonitored sport fishery exists in the vicinity of rkm 211 during runs. Other alevife are taken in Delaware Bay for use as crab bait and fertilizer. 5.2.2 BAY ANCHOVY Eay anchovy, Anchoa mitchilli (Appendix XII), a membar of the engraulid f amily, is a small, pelagic, schooling forage fith which inhabits estu-arine and inshore waters of the Atlantic and Gulf coasts from Maine to the Yucatan Peninsula, Mexico (Figure 5.2-3) . It is eurythermal and euryhaline, ar.d is probably the most abundant and ubiquitous fish in g Middle Atlantic estuaries including the Delaware system. It is an important link in energy transfer between trophic levels, as it consumes and converts biomass of small plankters and, in turn, is fed upon by predators including commercially important species such as striped bass, weakfish, and bluefish in Delaware Bay. The bay anchovy is relatively short-lived, with few rish surviving past their third year. Maturity is reached and spawning may occur near the end of the first year at a minimum length of 35-40 mm TL. The number of spawnings per season is not known, but batch fecundity ranges between approximately 2,000 and 4,000 eggs per, female in the Middle Atlantic region. Spawning season length varies wita latitude along the Atlantic coast. In the Delaware estuary, spawning occurs during May through September, with most during M2y through July between rka 0 and 48 at temperatures
>1700 and salinity >10 ppt.
Egg incubation requires about 24 hours at 27-280C. Size at hatching is about 2.0 mm TL; transition from pro- to post-larvae occurs near 3.0 cm TL. As the larvae develop, some are transported into lower-salinity nursery areas, most likely via net upstream subsurf ace currents. The larval growth rate may range from 0.45 to 0.68 mm/ day. Transformation of larvae to the juvenile stage occurs about 20 mm TL. ggg 5.2-2 EMII l l
Salen 316(b) Dem:nstrction Juveniles (0+ specimens) are typically first taken in the Delaware estu-
- ary in late June or July and are most abundant between late July and
< Ls-p/ i October. Their range extends frow shallow saline waters of the lower
- Bay to freshwater areas of the lower Delaware River (rka 145) (Figure l 5.2-4). Growth is rapid, of ten exceeding 0.3 mm/ day during summer months, and specimens attain a mean length of 57 mm FL by the end of their first year. During late fall or early winter, juveniles appar-ently move to deeper downbay waters.
Adults -(1+ and older) generally migrate from deep channel or nearshore ocean overwintering areas into shoal areas within the Delaware estuary during spring. They are usually most abundant between May and August. There is little growth (4-5 mm) during the second and third years. No - annually recurring pattern of movement within the estuary during spring and summer is apparent. In late summer or early fall, adults return to
- deep channel or nearshore ocean overwintering areas.
Based on its small size, early maturation, and production of large numbers of offspring, bay anchovy can be categorized as a " classic re-selected" species (McFadden et al.1978) . These factors should allow bay anchovy to withstand heavy exploitation and to reepond quickly to changes in the level of resources in the estuarine environment. 5.2.3 BLUEBACK HERRING Blueback herring, Alosa f estivalis (Appendix VI), is an anadromous
~ clupeid found in coastal ctreams and rivers from northern Florida to ; Nova Scotia and in a narrow band of coastal ocean waters to a depth of about 83 m (Figure 5.2-5) . It is a pelagic, schooling species. Adults congregate 'at the mouths of coastal rivers in late winter and early spring prior to upstream spawning runs. In.the Delaware system, blue-back herring run at least as far up the River ss rka 240 at Lambert-ville, New-Jersey, with strays reported as far north as rka 335 near Belvidere, New Jersey. No clearly discrete stocks have been identified either within the Delaware estuary or in other coastal river systems.
However, there is evidence that other clupeids--American shad and alewife--home to antal streams for spawning and that blueback herring probably.do also. In the Delaware River and its tributaries, spawning runs begin in April and May and extend through mid-June, typically peaking in early May. In Florida, spawning runs may begin as early as December; in New England ', streams, they are later and may extend into September. Within the Dels-ware estuary, spawning occurs in fresh or slightly brackish waters far 4 up tributary streams from the lower Bay to the fall line, and in the tidal Delaware River north of rka 189 (Figure 5.2-6). Spawning has been reported at temperatures from 14 to 270C, with peak spawning between 21 and 240C. Host blueback herring on spawning runs are ages 3 through 6. The maxi-mun age of blueback in Delaware runs is usually 7, =ith some age 8 or 9 occasionally occurring. Age 10 and 11 fis'n have been reported from x other areas. The mean length of spawning adults typically ranges from 220-241 mm FL, at age 3, through 241-281 mm FL, at age 7. 5.2-3 s 4
F E Salem 316(b) Demonstration ( i Fecundity per adult female collectad at Lambertville on the Delaware River ranged from 126,600 to 245,000 ovarian eggs. Based on other river systems, the reported extremes are 32,925 and 399,735. Egg retention g - l has been estimated as 9,300-107,600 eggs; these unspawned eggs eventu- 9.;k f i ally are absorbed. Many adults survive their first spawning experience e , and return to the ocean. Some may spawn up to six times in subsequent i. < years. Annual mortality of between 47 and 84 percent has been reported .V.i l in North Carolina. In the Delaware River, where mortality between two V ' sequantial adult age-classes could be calculated, it ranged from 44 to g, , 60 percent. s . .. ! Blueback herring eggs are initially adhesive and demersal, but are dis- SE[" lodged easily by flowing water and become pelagic. Incubation periods Q; range from 144 hours (at 16.200) to 28 hours (at 220C). Larvae may be g carried short distances downstream after hatching. Laboratory studies
~
on Delaware River larvae indicate that hatching occurs at 3-5 mm TL, t 2 with a growth rate of 0.15-0.68 mm/ day. The juvenile stage begins b. " approximately 35 days after hatching. Mortality rates have not been determined for blueback herring eggs and larvae. However, the mortal-
$W4 l ity rate for alewife, a rclated species, from egg through juvenile ggl emigration in fall has been estimated at.99.9987 percent in New England g.Q
> waters. i i
.?
Juveniles begin to leave the upper tidal Delaware River and its tribu- , taries when water temperature declines in September and October. Ley x. pass through the Artificial Island region (rka 82) primarily from late b.h October thrmgh early December and enter the lower Bay by mid-December. During the fall emigration, the juveniles are approximately 77-83 mm FL. gMTpjN
- Unusually heavy rains may flush new juveniles from tributary streams E into the lower River and Bay in spring or summer before typical emigra-tion would have occurred. Some juveniles overwinter in Delaware Bay, and others do so offshore. During winter and early spring, some juve-niles may move back upriver to and beyond the Artificial Island area.
E There is no local fishery specific to the marketing of blueback herring. g An unmonitored, altnough limited, sport fishery exists in the vicinity
- of rkm 211 during runs. Some blueback herring are taken in Delaware Bay g for use as crab bait and fertilizer.
E 5.2.4 ATLANTIC CROAKER Atlantic croaker, Microporonias undulatus (Appendix VIII), is a marine L sciaenid inhabiting coastal and offshore waters from Massachusetts to I Campeche Bank, Mexico (Figure 5.2-7). This schooling fish resides pri-r_ marily near the bottom, and migrates both inshore-offshore and north-
- . south over the course of the year. Both juveniles and adults use estuarine waters during summer and migrate offshore for overwintering.
- In the Delaware Bay, juveniles occur as far upriver as rkm 140, and the young are distributed throughout the Bay (Figure 5.2-8).
g Along the Atlantic coast, spawning takes place offshore over much of b the continental shelf and may extend from the mouth of Delaware Bay to Florida; major spawning appears to occur between Chesapeake Bay and g 5.2-4
Sslem 316(b) Demsrstrctice Cape Hatteras. Atlantic croaker spawn over a protracted period extend-ing from July to April. Fish entering Delaware Bay appear to have been O spawned between late August ar.d early October. of fehore, little is known about spawning activity, and inferences are Because spawning is generally based on larvae collections. The age at which Atlantic croaker nature differs throughout its distri-butional range. In the Chesapeake 8'ay/ Delaware Bay area, males reach maturity at the end of their second year, whereas females nature a year later. As these fish reach at least 4 years of age (age 6+ Atlantic croaker have been collected), the spawning contingent may consist of several age-classes. North of Cape Hatteras, about 50 percent cf the males and females are nature at lengths ranging from 187 to 224 mm TL and -185 to 233 mm TL, respectively. Atlantic croaker is a highly fecund species. Fecundity ranges from 100,800 to 1,742,000 ova per female for the population north of Cane Hatteres. The number of eggs shed during spawning is not known, nor is the fate of adults after spawning. Eggs are small (625-700 um in diameter) and apparently planktonic. , Following fertilization, embryonic development is completed in about 30 hours (200C), at which time larval emergence occurs. The larvae l are about 1.2 mm long at hatching. In North Carolina waters, Atlantic croaker larvae grow rapidly so that transition to the juvenile stage (11.0 mm TL) takes place at 35-40 days. Mortality rates fer larvae and early juveniles have been estimated to range from 0.03 to 0.08/ day. Juvenile Atlantic croaker remain in low salinity waters during their first year of life. During this time, they use the Delaware Bay and River as nursery and feeding grounds. As the fish approach 1 year, migration to offshore waters begins. Overwintering occurs offshore; but, in warm winters, a small fraction of the population appears to remain inshore. Yearlings return to the estuary the following spring, where they are distributed widely. These fish remain in the estuary throughout the summer, before migrating offshore in fall to spawn. This species is taken in commercial fisheries from New Jersey south throughout most of its range; major landings occur in the Chesapeake Bay area, North Carolina, and the northern Gulf of Mexico. In the
, Middle Atlantic region, croaker are usually caught in inshore waters from March until October. Spring catches representing the inshore migration of older fish of ten account for a considerable portion of the annual landings. Middle Atlantic Bight catches have been highly variable; recent catches appear to be increasing, although not in the Delaware Bay where croaker catches are of minor importance. The north-ern stock appears to fluctuate widely in response to climatic changes.
Although data on sport catches ave sparse, it appears that these catches contribute substantially to the total exploitation rate of the species. In Delaware, the trend in recreational landings has paralleled the com-mercial landings; few croaker were taken in 1980 an1 1981. C 5.2-5
Salem 316(b) Dem::nstrctica 5.2.5 AMERICAN SHAD American shad, Alosa sapidissima (Appendix III), is an anadromous clu-peid found in offshore waters and in coastal streams and rivers from Florida to Nova Scotia (Figure 5.2-9). It is a pelagic, schooling species. Adults congregate at the mouths of coastal rivers in late winter and early spring prior to upstream spawning runs. In the Dela-ware system, American shad run at least as far up the main River as rka 531 at Hancock, New York, and up the East Branch to rkm 552 (Figure 5.2-10). No clearly discrete stocks have been identified, although homing to natal streams for spawning has been strongly suggested by meristic differences among specinens from the Delaware and other East Coast river systems. Delaware River runs begin in March and April and extend into May. Spawning activity occurs from mid-April through June with peak activity in May. Ir Florida, spawning runs may begin as early as November; in Canada spawning is later and may continue as late as July. Within the Delaware estuary, spawning occurs in tidal fresh and nontidal waters, but the highest concentrations of spawning fish occur in nontidal waters between Dingman's Ferry, New Jersey (rkm 381), and Hancock, New York (rka 531). Eggs have been collected in the Delaware River only at rka 210 and 331. Spawning has been reported from 8 to 2600, with peak spawning between 14.8 and 22o0. Most American shad on spawning runs are age 3 through 6. The maximum age of shad in Delsware runs is 7 or 8, although sge 10 fish have been reported in other areas. The mean length of spawning adults ranges typically from 335-450 mm FL (at age 3) through 345-520 mm FL (at age 5), with a maximum size of about 580 mm FL. Fecundity for adult female shad in the Delaware River was approximated from length-frequency relationships and fecandity data from the northern and scuchern rivers nearest the Delaware as 287,385 for a typical age 4 female. Based on reports from other river systems, the extremes are 116,000 and 659,000. Egg retention has been estimated to range from approximately 11,000 to 36,000 eggs; these unspawned eggs are eventually absorbed. In rivers north of Cape Fear, North Carolina, some adults survive spawning, return to sea, and may spawn again in subsequent yeart up to a maximum of about three times. With the Delaware River, 0.3-10 percent return to spawn again. Annual mean mortality for adult Delaware River American shad was calculated at approximately 72 percent. Eggs are initially adhesive and demersal, and (depending on the bottom-type) either become lodged in bottom rubble or roll along with stream flow. Incubation periods range from 2 days (at 270C) to 17 days (at 120C). Larvae may be carried short distances downstream after hatching. American shad larvae are reported to hatch at 5.7-10 mm TL, and enter the juvenile stage approximately 21-28 days af ter hatching. Mortality rates have not been determined for eggs. Mortality for larvae has been estimated at 98.3-98.9 percent. has been estimated at 99.99943 percent. The mortality rate from egg to adult g 5.2-6 1
( Sales 316(b) Densnatretion Juveniles begin to leave the upper Delaware River when water temperature declines in September and 0:tober. They pass through the Artificial O Island region (rka 82) primarily from late October through mid-December and enter the lower Bay by late December and January. During the fall emigration, they are approximately 90-94 mm FL. Some juveniles over-winter in Delaware Bay, but most move offshore and remain there until nature. During late winter and early spring, some juveniles may move back upriver to and beyond the Artificial Island area. In the Delaware system, American shad are exploited by both a commercial and a sport fishery during the spawning run. Decreased market demand for shad has prompted a steeply downward long-term trend in commercial fishing efforts. Recent exploitation rates for the Delaware system fishery range from 11.3 to 29.2 percent of the spawning population. This rate is considerably lower than river systems to the south, because the local market is saturated by fish from those areas before shad become available to the Delaware commercial fishery. In contrast, the sport fishery has increased dramatically. The exploitation rate cur-rently is estimated at 8.5 percent of spawners. The Delaware Basin Fish and Wildlife Management Cooperative (1980) shad management plan for the Delaware system targets the commercial fishery at 20 percent of the spawning population and at 10 percent for the sport fishery. 5.2.6 SPOT Spot, Leiostomus xanthurus (bppendix VII), a member of the drum family, is a euryhaline marine species that inhabits inshore coastal and estu-s arine waters of the Atlantic and Gulf coasts from Massachusetts Bay to the Bay of Campeche, Mexico (Figure 5.2-11). Greatest population abun-dance along the Atlantic coast occurs from Virginia southward. Earliest life stages occur in offshore shelf waters, whereas the juvenile stage is estuarine-dependent and utilizes the numerous estuaries, including the Delaware estuary, throughout the range as nurserv. Older spot may remain year-round in coastal waters or migrate seasonally into bays or sounds. Spot is relatively short-lived, erith a life span seldom longer than 3 years; the maximum recorded age is 5.5 years. The annual mortality rate for adult spot is estimated to be 80 percent or greater. Maturity is presumed reached at the end of the second year (or early in the third) and at a minimum length of approximately 160 mm TL. Fecundity is essen-tially undefined, but reportedly may range from about 80,000 to 377,000 ova. Spawning siong the Atlantic coast, as inferred from capture of early larvae, occurs over the continental shelf from North Carolina to north-era Florida but may, under certain conditions, occur northward to pos-sibly the offing of Delaware Bay. The season is protracted, extending from perhaps late September through March; peak spawning activity is believed to occur during December and January. In laboratory studies, incubation took from 22 hours (at 2700) to nearly 100 hours (at 150C); p- hatching size is about 1.5 usa TL. Larvae develop in the shelf waters and, by a combination of svisuming and passive transport via ocean cur-rents, move; shoreward toward estuarine waters. Larval growth reportedly 5.2-7
l Sclem 216(b) Dem:nstrction ranges from 0.1 to 0.3 mm/ day. Transformation to the juvenile stage occurs just prior to or during estuarine immigration, with size and age at entrance reportedly increasing progressively with distance from g North Carolina. Estuarine recruitment may occur over several months. Juveniles dieperse quickly thoughout the estuary, but are typically most abundant in areas characterized by shallow water, mud bottom, and reduced salinity. Apparently, the daily instantaneous mortality rate cf juveniles varies by location; in North Carolina nursery areas, estimates for early juveniles range from 0.028 to 0.061. Juvenile growth is rapid, well exceeding 0.25 mm/ day during summer months, and average fork length at year's end is 120-150 mm. Depending on the geographic region, juveniles may remain in estuarine waters or move offshore during late fall /early winter. Large winter kills of juve-niles occur occasionally, especially in more northerly estuaries. Spot 0+ enter Delaware Bay as early joveniles (20-30 mm FL) as early as April, and abundance increases through continued recruitment into June. They disperse to upriver, the shore zons of the Bay, and into nearly all tributaries of the lower drainage. Young spot usually appear in the lower River (rkm 64-100) during mid-May, and by late Juno this uprivar component is concentrated beyond rka 117 (Figure 5.2-12). With declining water temperature during f all, these fish move back downbay. Passage through the Artificial Island area is usually during October through December. Occasionally, during mild winters, some juveniles may overwinter in deeper Bay waters; typically, spot move offshore and presumably southward to overwintering grounds in the South Atlantic region. This is evidenced by their abaeure during winter in coastal g waters within the Middle Atlantic region (h2w York to Virginia) coupled W with the winter recapture off North Carolina of spot tagged from Chesa-peake and Delaware bays. The occurrence of spot 1+ and older in the Middle Atlantic region is also eensonal. These spot migrate northward into this region during spring from vinter spawning grounds and, after summering in estuarine and inshore coastal waters, depart during early fall to waters off the Caro; 5 na s. These older fish grow more slowly than do the 0+; and age 1+ and 2+ attain lengths of 190-240 and 210-260 mm FL, respectively. Spot 1+ and older occur Rypically in the Delaware estuary from July through September, in much lower abundance than age 0+, and generally remain in the Bay. Spot populations are subject to Isrge annual fluctuations in abundance, of ten varying by an order of magnitude. Annual fluctuations are also evident in the Delaware estuary. Speculation is thct these variations in year-class strength may reflect environmental conditions on the spawning grounds. Spot is of minor commercial and recreational importance in the Delaware Bay, but is a valuable component of fisheries along the Atlantic coast south of Maryland and in the Gulf of Mexico. Besides being harvested as a foodfish, spot is exploited in the industrial groundfish fishery; vast quantities also are caught and discarded (dead) at sea by shrimping ggg operations. 5.2-8
Salem 316(b) Demonstration i str b se rg_n_e saxatilis (Appendix IX), is an anadromous 4 fish that inhabits primarily estuarine and nearshore coastal vatars of the Atlantic and Gulf coasts from the St. Lawrence River, Canada, to Louisiana (Figure 5.2-13). It is semidemersal and occurs in rocky i nontidal rivers and shallow bays, and along sandy surf-swept beaches i and rocky shores. The greatest population abundance along the Atlantic ,
- coast occurs from Cape Cod to North Carolina. The striped bass is adaptable, and populations have been established in fresh water and along the Pacific coast. In the Delaware dusinage, juveniles and adults may occur from the ocean off Delaware Bay, into the Bay and tidal River, and, rarely, above the fall line (rka 220) to Belvidere, New Jersey ,
(rka 317) (Figure 5.2-14). Early life stages occur principally in the lower Delaware River in, or north ef, the Chesapeake and Delaware l (C&D) Canal / Pea Patch Island region (rha 95-97) . A number of distinct i estuary-specific spawning populations have been identified along the i Atlantic coast based on morphological and biochemical differences. Striped bass in long-lived, of tea attaining 14-15 years and occasionally
- about 30 years. Females are generally larger and live longer; most fish '
over 11-years are female. Males nature younger and at a smaller sice than females. Minimum reported lengths at maturity are 174 mm TL for males and 432 mm TL for females. In general, males nature during their second or third year, and females by their fif th or sixth. Nature females may not spawn every year. Fecundity estimates range from 15,000 eggs in a 46-cm fish to 4,864,000 in a 116-cm specimen. i Prespawning striped bass begin to move toward spawning areas--generally located within the first 40 km of fresh water in tidal river systems-i during late winter through early summer (depending on latituda) and l . arrive just prior to the spawning season. Males arrive first, usually having remained in or near the estuary, whereas females have returned i to their natal rivets from coastal waters. Striped bass may spawn in mid-February in Florida and as late as June or July in the Gulf of St. Lawrence and lower St. Lawrence River. Spawning in Chesapeake Bay, which with its major tributaries comprises the principal spawning-nursery grounds for striped bass along the Atlantic coast, occurs principally in April, but also in May and early June.
- l. Historically, the entire tidal freshwater reach of Delaware River, including some tributaries, was utilized by striped bass as spawning grounds. Since the early 1900s, however, both the spatial extent and the intensity of spawning in the Delaware system have been reduced greatly as a result of degraded water quality and habitat; striped bass production in the Delaware is now considered minimal. There is l considerable spawning in the western end of the Chesapeake and Delaware r
l- (C&D) Canal by fish of the upper Chesapeake Bay population, and subse-l quent transport of some of this production by the Canal's net easterly l flow is generally accepted as the source of most of the relatively few l striped bass eggs, larvae, and yearlings that occur in the Delaware River. Spawning in the C&D Canal occurs mostly during mid-April through lQ V mid-May and typically is characterized by a short period of intense activity at water temperatures of 13.5-17.40C. 5.2-9
Salen 316(b) Dersnstrction Striped bass eggs are nonadhesive and semibuoyant, and their survival requires a current velocity >0.3 m/sec. Incubation takes from 65 hours at 150C to 24 hours at 24oC. Hatching occurs at 2.0-3.7 mm TL; trans-g formation to the juvenile stage occurs at 16-20 mm TL about 20-60 days af ter hatching, depending on water temperatuce. Based on evidence from the Hudson River, growth is relatively slow during early larval stages (0.1-0.2 mm/ day; mid-May through mid-August), but increases considerably during the, late larval and early juvenile stages (0.8-0.9 mm/ day; mid-June through mid-August). Daily instantaneous mortality rate of larvae in the Hudson River has beca estimated as 0.1924-0.1625, and of late larvae /early juveniles as 0.0523. The extent to which early life stages of striped bass are transported by water currents appears to be system-specific. Transport is considerable in the Hudson River and C&D Canal, whereas larvae and early juveniles in the Potomac estuary apparently remain most abundant in areas of peak spawning or even farther upstream despite continued downstream water flow. In essentially all striped bass population studies, late-stage larvae and early juveniles move from the deep channel waters to inshore nursery areas as development continues. In the Middle Atlantic region, striped bass 0+ reach lengths of approximately 100 mm TL by November or December. Age 0+ striped bass have been evidenced to move generally to deeper waters in the fall and to overwinter in lower tidal rivers or adjacent bays and sounds. During the following spring, age 1+ fish leave over-wintering areas, with some remaining in the Delaware River while others move downstream toward the ocean. In summer, age 1+ fish are distri-buted throughout the tidal river and lower bays of their natal estuaries and are most abundant in the shore zone. During fall, these fish move g into deeper waters and toward overwintering sites, principally in the lowest estuary, although some may overwinter in upriver channel areas. Striped bass 0+ through 3+ or 4+ use the lower Delaware River and its tidal tributaries as a nursery and foraging area during summer and over-winter in the deeper waters of the lower River and upper Bay. Since the early 1970s, most striped bass taken in the Artificial Island region (rka 80) have been during Inte fall through late winter. A portion of the striped bass 2+ and older between Cape Hatteras and New England leave their natal estuaries and enter an Atlantic coastal migra-tion consisting of groups of primarily female fish moving along the open coast, rarely more than a few miles from shore, generally northward in spring and southward in fall and winter. Striped bass support important commercial and recreational fisheries throughout most of its range. Along the Atlantic coast, the principal commercial fisheries occur from Massachusetts through North Carolina; Maryland leads all states in landings. Atlantic coast landings, which hcd followed a generally rising trend since 1928, peaked in 1973 at 6,683 metric tons. Subsequent landings declined steadily through 1979 and rose slightly ir 1980. The annual recreational catch of striped bass in 1960,1965,1970, and 1979 (the only years it was monitored on a coastwide basis) exceeded respective commercial landings by more than fivefold. Presently in the Delaware estuary there is essentially no ggg dir~ected commercial fishery for striped bass. Most of those entering the commercial catch are taken incidentally in the white perch and 5.2-10 l
Solen 316(b) Densnetretion American shad gill net fisheries. The 1981 Delaware gill net landings were 10.2 metric tons valued at $19,125. Sport fishing ef fort for O striped bass in Delaware River, although limited, is typically concen-trated in the C&D Canal; the Port Penn to Augustine teach, Delaware, i reach of the River; and at the mouths of the principal tributaries south of the C&D canal. 5.2.8 WEAKFISH Weakfish, Cynoscion reaalis (Appendix XI), a member of the drum family, is a schecling marine migrant which feeds and spawns during summer in sounds and bays from Cape Cod to Florida (Figure 5.2-15). In winter, weakfish congregate offshore of North Carolina .e4 "li lula. Beginning in March, age 4+ and older fish migrate inshore and up the coast, fol-loved by successively younger age groups. Weakfish generally inhabit the Delaware estuary from April through November (Figure 5.2-16). Adults spawn and feed primarily in the lower estuary, i.e. , Delaware Bay, while age 0+ young use the Bay and lower River to about rka 100 as a nursery area. Beginning in May, age 3+ and 4+ spawn, leave the Bay, and are replaced by progressively younger fish; by August, age 1+ fish dominate. -Beginning in early autumn, weakfish move out of estuaries toward their wintering grounds, possibly following the 160C isotherm as it moves offshore and southward. Two or three breeding populations have been hypothesized on tne basis of differences in growth and meristics, but evidence is inconclusive. , /' The most recent study suggests one genetically homogeneous population, at least during periods of high abundance. Weakfinh grow to about 750 mm TL and reach a maximum weight of about 6 kg. Maxisma age is 11 years; fish up to nine years of age have been taken in Delaware Bay. Adult growth rate and longevity are greater in the northern part of the species range. Most males and females are nature by their second summer (age 1+); virtually all are mature by the end of their third summer (age 2+). Fecundity increases with age and ranges from 5,000 to over 2 million eggs per female. Northern ***h are less fecund at each length than southern fish. Weakfish are nocturnal broadcast spawners. Spawning occurs nearshore, along coasts, and in bays at temperatures between 14 and 250C and within a salinity range of 12.0-32.5 ppt. In Delaware Bay, the season extends from May through August and is most pronounced in late May and June. Secondary spawning peaks occur during some years in July. The center of spawning activity shif ts progressively from the southwestern part of the Bay including the Brandywine shoal region (rka 18) early in the season.to the Port Mahon region (rka 47) as the season progresses. Eggs are buoyant and hatch in about two days. Annual production estimates for Delaware Bay range from 1.5 to 8.7 trillion eggs. O 5.2-11
Salem 316(b) Demonstrction Prolarvae are planktonic and range in size from 1.49 to 1.99 mm TL upon hatching. Af ter about 6 days, they lose buoyancy and transform into postlarvae. Bottom currents transport them up-estuary to the upper Bay g and lower River. Duration of the postlarval stage is about 8 deys. Age ^^ young are found generally up-estuary from earlier life phases. In tne present study, young were distributed throughout the Bay and lower River (rkm 0-117) each year between June and August, with peak densities occurring at various locations throughout the Bay. Growth averages 1.1 mm per day in summer, but slows or stops in winter. - Most exit the Delaware River and Bay by November; all are gone by mid-December. Sexual maturity is reached at age 2-4 years. Adult weakfish in Delaware Bay generally occur between rkm 0 and 80, but are most abun-dant in the southwestern Bay offshore of the Mispillion River (rkm 19). The weakfish supports important commercial and recreational fisheries throughont its range. Most of the commercial catch is taken in Virginia and North Carolina, whereas most of the recreational catch occurs from Delaware Bay to New York. Atlantic coast commercial landings have fluctuated widely, but remained above the 50 year average of 15,000,000 pounds since 1975. In 1982, Delaware's commercial fishery landed 1,300,000 pounds of weakfish valued at $757,000 at dockside with a total economic impact of $2.2 million including retail sales and wages. Nearly all of the catch is taken in Delaware Bay. The Bay may be equally important to New Jersey, but comparable statistics are not available. The importance of weakfish to Delaware and New Jersey sport fisheries fluctuates with species abundance. Periodic surveys by Delaware Depart-ment of Natural Resources and Economic Commiraion since 1955 show that weakfish comprised from 4.4 to 54.4 percent of the total catch. The estimated 114,178 landed in 1982 comprised 15.1 percent of the total catch for the State of Delaware. The economic impact to Delaware of the 1982 sport fishery (all species, all Delaware marine waters plus spring fishery in New Jersey part of the Delaware Bay) is estimated at over
$12.8 million. A comparable value for New Jersey is not available.
5.2.9 WHITE PERCH White perch, Morone americana (Appendix I), occur predominantly in brackish water from South Carolina to Nova Scotia (Figure 5.2-17). They are most abundant between Hudson River and Chesapeake Bay. Land-lockri freshuater populations occur in coastal ponds and lakes, espe-cially in the northern part of the range; they also occur in the 1 Lower Great Lakes and some midwestern reservoirs. In the Delaware system, white perch inhabit the area from rkm 0 to approximately rkm 330, but do not occur regularly above rkm 280 (the Musconetcong River) and are relatively uncommon below rka 35 (Figure 5.2-18) . Most of the tidal tributaries contain white perch populations. These tributaries may support discrete populations, as has been found to occur in Chesapeake Bay. O 5.2-12
Sclem 316(b) Demonstration Average life span for white perch is estimated at 5-7 years; however, they can live as long as 17 years. In general, lacustrine populations have a longer life span than estuarine ones. In the Delaware River, th( maximum age is 8-10 years, but the majority of the population is 4 years old or younger. Sexual maturity in the Delaware system is attained at ages 2-3 for males and 2-4 for females. Maturity may occur later in populations farther north. In the Delaware, all males above about 110 mm SL and all females above 130 mm SL were mature. The fecundity of white perch ranges from 20,000 to 250,000 eggs per adult female and increases with increasing fish size. Peak production, as eggs per gram of ovarian tissue, occurs between 3 and 4 years of ege (based on data from the nearby C&D Canal). Egg retention also appears to be related to age. An estimate from the Hudson River population indicates 35 percent retention for age 3, decreasing to 10 percent at age 4. Spawning takes place at temperatures ranging from 10 to 1900, with the average at about 15-160C. In the Delaware region, spawning occurs from early April through early June. In the mainstem of the River, spawning in most common upstream of Newbold Island (rka 201) and may occur as far north as Lambertville (rka 233). Spawning also occurs in the tributary creeks and rivers and in the C&D Canal. In the latter, spawning takes place primarily in tributaries located at the western end. White perch eggs are rarely taken in the mainstream River near Artificial Island. In early spring, adults typically move upriver to low-salinity waters ( 'O -from the deeper, more saline overwintering grounds. "lggs are usually deposited in shallow areas and are demersal, generally found attached to rocks, grass, and debris. The incubation period is inversely related to temperature, with a lower limit (around 7.2oC) below which develop-ment stops. At 10-150C, eggs hatch in about 3-4 days into prolarvae approximately 2.6 mm TL. The transition to postlarvae occurs 3-5 days after hatching at a length of 3.5-4.0 mm TL. The larval stages are planktonic, preferring bottom waters, particularly during the day. They disperse throughout the water column at night. Being planktonic, white perch larvae are subject to the currents and drift downstream from the spawning location. Development to the juvenile stage takes approxi-mately six weeks. Size at transition ranges from 15 to 30 mm TL, with most showing juvenile features by 20 mm TL. At some point during the transition from postlarvae to juveniles, young white perch move inshore to shallow-water nursery areas where they spend the remainder of the summer. During fall, most juveniles leave the tributaries and upriver nursery areas to overwinter in deeper, more saline waters. Based on recaptures of marked fish during the present study, a large portion of the upriver-spawned young of the year over- , vinter in the Delaware estuary north of Salem. Adults also move to deeper, saline water and, in fact, are taken in the lower Bay only during late fall and winter. l White perch larvae and young juveniles are primarily planktivorous; they also feed on epibenthic organisms such as amphipods, crustaceans, insects, and, as they grow larger, on fish eggs. To a limited degree, 5.2-13
Salem 316(b) Dem:nctration adult white perch also consume other fish. Studies in Delaware Bay and its tributaries indicate that the most com.nonly eaten prey items are Neomysis americana, Gammarus spp., and copepods. The latter were con-g sumed only by white perch <90 mm TL. In estuaries, competitors of larval and juvenile white perch include striped bass, American shad, alewife, blueback herring, weakfish, spot, and croaker. Striped bass also prey on juvenile white perch. White perch are exploited by both commercial and sport fisheries. They are caught by sport fishermen in the headwaters of tributary streams i during the spring spawning runs. Commercial fisheries also selectively exploit white perch during this period. Fishing effort and, conse-quently, landings in Delaware, have declined sharply since the turn of the century, probably as a result of decreased demand. There are no indications that the catch has been limited by stock size. Recent surveys indicate that a majority of the commercial effort occurs in the reFions of Port Mahon and Bowers Beach. e e 5.2-14 l l
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Salem 316(b) Demonstration LITERATURE CITED: q SECTION 5 Allen, D.M. 1978. Population dynamics, spatial and temporal distributions of mysid crustaceans in a temperate marsh estuary. Doctorate. Thesis. Lehigh Univ. , Bethlehem, Pa. 157 pp. Clutter, R.I. and G.H. Theilacker. 1971. Ecological efficiency of a pelagic mysid shrimp; estimates from growth, energy budget, and mortality studies. Fish. Bull. 69(1). Cronin, L.E., J.C. Daiber, and E.M. Hulburt. 1962. Quantitative seasonal aspects of zooplankton in the Delaware River estuary. Chesapeake Sci. 3(2):63-93. Delaware Basin Fish and Wildlife Management Cooperative (DBFWMC). 1980. Strategie Management Plan for the American Shad (Alosa sapidissima) in the Delaware River Basin. Delaware River Basin Authority, Trenton, N.J. 132 pp. Doylc, R.W. and W. Hunte. 1981. Demography of an estuarine amphipod (Gammarus lawrencianus) experimentally. selected for high "r": A model of the genetic effects of environmental change. Can. J. Fish. Aquat. Sci. 38:1120-1127. ( )I Hulburt, E.M. 1957. The distribution of Neomysis americana in the Limnol. Oceanogr. 2(2):1-11. estuary of the Delaware River. Hynes, H.B.N. 1955. The preproductive cycle of some British freshwater Gammaridae. J. Anim. Ecol. 24:352-387. McFadden, J.T. , Texas Instruments, Inc. , and Lawler, Matusky and Skelly Engineers. 1978. Influence of the proposed Cornwall pumped storage project and steam electric generating plants on the Hudeon River estuary with emphasis on striped bass and other fish populations. Prepared for Consolidated Edison Company of New York, Inc. Wigley, R.L. 1064. Mysidaceae, i3t Keys to Marine Invertebrates of the Wcods Hole Region (R.I. Smith, ed.), pp. 93-97. Marine Biological Labor atory, Woods Hole, Mass. (_/ 4 _ __ 1
Salem 316(b) Demonstration G SECTION 6: ENTRAINMENT AND IMPINGEMENT O O
Salem 316(b) Demonstration SECTION 6: ENTRAINMENT AND IMPINGEMENT Page, LIST OF TABLES LIST OF FIGURES 6.1 ENTRAINMENT 6.1-1 6.1.1 The Entrainment Process and Target Species 6.1-1 6.1.2 Entrainment Densities 6.1-3 6.1.2.1 Methods Used to Estimate Entrai==ent 6.1-4 Densities 6.1.2.2 Estimated Entrainment Densities 6.1-5 6.1.3 Entrainment Survival Rates 6.1-11 6.1.3.1 Methods Used to Estimate Entrainment 6.1-11 Survival Rates 6.1.3.2 Estimated Entrairment Survival Rates 6.1-13 6.1.4 Estimating the Rate of Entrainment Losses 6.1-23 6.2 IMPINGEMENT 6.2-1 6.2.1 The Impingement Process and Target Species 6.2-1 6.2.2 Impingement Densities 6.2-2 6.2.2.1 Methods Used to Estimate Impingement 6.2-2 Densities 6.2.2.2 Estimated Impingement Densities 6.2-4 6.2.3 Impingement Survival Rates 6.2-9 6.2.3.1 Methods Used to Estimate Impingement
- 6.2-10 Survival Rates 6.2.3.2 Estimated Impingement Survival Rai is 6.2-11 6.2.4 Estimating the Rate of Impingement Losses 6.2-16 6.2.4.1 Spot 6.2-17 6.2.4.2 Blueback Herring 6.2-18 6.2.4.3 Alewife 6.2-19 6.2.4.4 American Shad 6.2-19 6.2.4.5 Atlantic Croaker 6.2-20 i (_,g7- J 6.2.4.6 Striped Bass 6.2-20 6.2.4.7 White Perch 6.2-21
Salem 316(b) Demonstration SECTION 6: ENTRAINMENT AND IMPINGEMENT Page 6.2.4.8 Bay Anchovy 6.2-21 6.2.4.9 Weakfish 6.2-22 6.3 ESTIMATES OF RELATIVE CROPPING FOR TARGET SPECIES 6.3-1 6,3.1 Introduction 6.3-1 6.3.2 Modeling Approaches for Entrainment and 6.3-3 Impingement 6.3.2.1 Empirical Transport Model 6.3-3 6.3.2.2 Empirical Impingement Model 6.3-6 6.3.2.3 Exploitation Rate Approach 6.3-8 6.3.2.4 Equivalent Adult Approach 6.3-11 6.3.2.5 Production Foregone Approach 6.3-12 6.3.2.6 Lost Reproductive Potential Approach 6.3-13 6.3.2.7 Selection of Modeling Approaches 6.3-15 for Target Species 6.3.3 Methods for Developing Model Input 6.3-17 6.3.3.1 ETM Model Input Parameters 6.3-17 h 6.3.3.2 EIM Model Input Parameters 6.3-19 6.3.3.3 Exploitation Rate Approach Input 6.3-19 Parameters 6.3.3.4 Equivalent Adult Approach Input 6.3-19
- Parameters 6.3.3.5 Production Foregone Input Parameters 6.3.3.6 Lost Reproductive Potential Approach Parameters 6.3.4 Estimates of Relative Cropping 6.3-20 6.3.4.1 Blueback Herring 6.3-20 6.3.4.2 Alewife 6.3-22 6.3.4.3 American Shad 6.3-23 6.3.4.4 Spot 6.3-24 5.3.4.5 Atlantic Croaker 6.3-27 6.3.4.6 Striped Bass 6.3-28 6.3.4.7 Neomysis Americana 6.3-28 6.3.4.8 The Gammarus Tigrinus Group 6.3-30 6.3-31 6.3.4.9 White Perch 6.3.4.10 Bay Anchovy 6.3-34 6.3.4.11 Weakfish 6.3-38 6.4 POTENTIAL BIASES IN IMPINGEMENT AND ENTRAINMENT ESTIMATES 6.4-1 LITERATURE CITED
Salem 316(b) Demonstration ()* LIST OF TABLES: SECTION 6 Number Title 6.1-1 Rank and percent total catch of macroinvertebrate plankton, 1978. 6.1-2 Estimated entrainment densities of Neomysis americana and Gammarus spp. at the Salem Generating Station from entrainment abundance program, 1977-1980. ! 6.1-3 Species composition of ichthyoplankton entrainment samples at the Salem Generating Station, 1978-1981. 6.1-4 Estimated egg entrainment densities of fish species at the Salem Generating Station from entrainment abundance program, 1977-1982. 6.1-5 Estimated larval entrainment densities of fish species at the Salem Generating Station from entrainment abundance program, 1977-1982. 6.1-6 Estimated juvenile entrainment densities of fish species at the Salem Generating Station from entrainment abundance ('~ ) program, 1977-1982. 6.1-7 Estimated adult entraimnent densities of fish species at the Salen Generating Station from entrainment abundance l program, 1977-1982. 6.1-8 Comparison of Neomysis americana mean densities found in circulating water system to those found in Delaware River. 6.1-9 Projected monthly entrainment densities of Neomysis americana based on estbnated river densities and E/R ratios. 6.1-10 Comparison of Gammarus tigrinus group mean densities found in circulating water system to those found in Delaware River. 6.1-11 Projected monthly Gammarus tigrinus group entrainment density based on estimated river densities and E/R ratios. 6.1-12 Projected weekly entrainment densities for secondary target species. (~m Projected weekly entrainment densities for primary target ( ,) 6.1-13 species.
l ) Salem 316(b) Demonstration dumber Title 6.1-14 Summary of entrainment mortality: spot early juvenile operation history: no outage. 6.1-15 Summary of entrainment mortality: blueback herring early juvenile operation history: no outage - low mortality estimates. 6.1-16 Summary of entrainment mortality: blueback herring early juvenile operation history: no outage - high mortality es timates . 6.1-17 Summary of entrainment mortality: Atlantic croaker juveniles operation history: no outage. 6.1-18 Summary of entrainment mortality: striped bass eggs operation history: no outage. 6.1-19 Swnmary of entrainment mortality: striped bass larvae operation history: no outage, 6.1-20 Swamary of entrainment mortality: white perch prolarvae operation history: no outage. 6.1-21 Summary of entrainment mortality: white perch postlarvae operation history: no outage. 6.1-22 Summary of entrainment mortality: bay anchovy juveniles and adults operation history: no outage. 6.1-23 Summary of entrainment mortality: weakfish prolarvae and postlarvae operation history: no outage. 6.1-24 Summary of entrainment mortality: weakfish juveniles operatim. history: no outage. 6.1-25 Summary of entrainment mortality: Neomysis americana operation history: no outage. 6.1-26 Summary of entrainment mortality: Gammarus sp. operation history: no outage.
~
6.1-27 Projected number of CWS pumps operating each week at Salem Units No. I and 2 under various outage schedule for 100 percent power and pumping except during refueling. 6.1-28 Projected number of CWS pumps operating each week at Salem Units No. I and 2 under various outage schedule for typical full-power operation. 6.1-29 Estimated rate of entrainment losses of spot - early juvenile: no outage, s
i Salem 316(b) Demonstration Number Title 6.1-30 Estimated rate of ent ainment losses of blueback herring - early juvenile: no outage - low mortality estimate. 6.1-31 Estimated rate of entrainmeat losses of blueback herring - early juvenile: no outage - high mortality estimate. 6'.1-32 Estimated rate of entrainment losses of alewife - early juvenile: no outage - low mortality estimate. 6.1-33 Estimated rate of entrainment losses of alewife - early juvenile : no outage - high mortality estimate. 6.1-34 Estimated rate of entrainment losses of Alosa spp. - early juvenile: no outage - low mortality estimate. 6.1-35 Estimated rate of entrainment losses of Alosa spp. - early juvenile: no outage - high mortality estimate. 6.1-36 Estimated rate of entrainment losses of Atlantic croaker - larvae . no outage. 6.1-37 Estimated rate of entrainment losses of Atlantic croaker - juveniles: no outage. 6.1-38 Estimated rate of entrainment losses of striped bass - eggs: no outage. 6.1-39 Estimated rate of entrainment losses of striped bass - larvae: no outage. 6.1-40 Estimated rate of entrainment losses of white perch - prolasvae: no outage. 6.1-41 Estimated rate of entrainment losses of white perch - postlarvae: no outage.
-6.1-42 Estimated rate of entrainment losses of bay anchovy -
eggs: no outage. 6.1-43 Estimated rate of entrainment losses of bay anchovy - larvae: no outage. 6.1-44 Estimated rate of entrainment losses of bay anchovy - juveniles / adults: no outage. 6.1-45 Estimated rate of entrainment losses of weakfish - eggs: no outage. {~~')
/ . 6.1-46 Estimated rate of entrainment losses of weakfish -
prolarvae: no outage.
Salem 316(b) Demonstration Number Title llh 6.1-47 Estimated rate of entrainment losses of weakfish - postlarvae : no outage. 6.1-48 Estimated rate of entrainment losses of weakfish - juveniles: no outage. 6.1-49 Estimated rate of entrainment losses of Neomysis ameri-cana: no outage. 6.1-50 Estimated rate of entrainment losses of Gammarus sp.: no outage. 6.1-51 Summary of estimated rates of entraimsent losses for ichthyoplankton target species under various plant operating conditions. 6.1-52 Summary of estimated rates of entraimment losses for macroinvertebrate target species under various plant operating conditions. 6.2-1 Species composition of impingement samples at the Salem Generating Station, 1978-1982. 6.2-2 Impingement densities at the Salem Generating Station, 1977-1982. lll 1 6.2-3 Age composition of bay anchovy in Salen impingement sempling, 1977-1982. 6.2-4 Age composition of white perch in Salem impingement sampling, 1977-1982. 6.2-5 Age composition of alewife in Salem impingement sampling, 1977-1982. 6.2-6 Age composition of blueback herring in Salem impingement sampling, 1977-1982. 6.2-7 Age composition of spot in Salem impingement samples, 1977-1982. 6.2-8 Age composition of weakfish in Salem impingement samples, 1977-1982. 6.2-9 Age composition of striped bass in Salem impingement sampling, 1977-1982. 6.2-10 Summary of observed monthly mean impingement density of spot at Salem under greater than 2 pump operating condi- llh tions and estimates of future monthly densities using various averaging procedures.
Salem 316(b) Demonstration () Number Title 6.2-11 Summary.of observed monthly mean impingement density of blueback herring at Salem under greater than 2-pump operating conditions and estimates of future monthly densities using various averaging procedures. 6.2-12 Summary of observed monthly mean impingement density of alewife at Salem under greater than 2-pump operating conditions and estimates of future monthly densities using various averaging procedures. 6.2-13 Summary of observed monthly mean impingement density of American shad at Salem under greater than 2 pump opera-ting conditions and estimates of future monthly densities using various averaging procedures. 6.2-14 Summary of observed monthly mean impingement density of l Atlantic croaker at Salem under greater than 2- pump operating conditions and estimates of future monthly densities using various averaging procedures. l
- i. 6.2-15 Summary of observed monthly mean impingement density of striped bass at Salem under greater than 2 pump operating conditions and estimates of future monthly densities
() using various averaging procedures. 6.2-16 Summary of observed monthly mean impingement density of white perch at Salem under greater than 2 pump operating conditions and estimates of future monthly densities using various averaging procedures. 6.2-17 Summary of observed monthly mean impingement density of bay anchovy at Salem under greater than 2 pump operating conditions and ('timates of future monthly densities using various averaging procedures. 6.2-18 Summary of observed monthly mean impingement density of weakfish at Salem under greater than 2-pump operating conditions and estimates of future monthly densities using various averaging procedures. 6.2-19 Estimated monthly initial, latent, and total mortality of spot 0+ taken in Salem impingement samples, 1977-1982. 6.2-20 Estimated initial, latent, and total mortality by age of blueback herring taken in Salem impingement samples, 1977-1982.
-6.2-21 Estimated initial, latent, weighted latent, and total
() mortality by age of alewife taken in Salem impingement samples, 1977-1982. 1
n 316(b) Demonstration Number Title 6.2-22 Estimated monthly initial, latent, and total mortality y age of American sha.., taken in Salem impingement samples, 1977-1982. 6.2-23 Estimated monthly initial, latent, and total mortality of Atlantic croaker taken in Sal m impingement samples, 1977-1982. 6.2-24 Estimated monthly initial, latent, and total mortality by age of striped bass taken in Salem impingement samples, 1977-1982. 6.2-25 Estimated monthly initial, latent, and total mortality of white perch taken in Salem impingement samples, 1977-1982. 6.2.26 Monthly initial, latent, and total morr .ty of pooled age bay anchovy taken in Salem impingement samples, 1977-1982. 6.2-27 Estimated monthly initial, latent and total mortality of weakfish taken in Salem impingement samples, 1977-1982. 6.2-28 Projected number of CWS pumps operating each month under various outage schedules for Salem Units No. 1 and 2. 6.2-29 Predicted number of CWS pumps operating under various outage schedules for Salem Units No. 1 and 2. (Typical full-power operation.) 6.2-30 Expected mean rate of impingement losses of spot. 6.2-31 Expected mean rate of impingement losses of blueback herring. 6.2-32 Expected mean rate of impingement losses of alewife. 6.2-33 Expected mean rate of impingement losses of American shad. 6.2-34 Expected mean rate of impingement losses of Atlantic croaker. 6.2-35 Expected mean rate of impingement losses of striped bass. 6.2-36 Expected mean rate of impingement losses of white perch. 6.2-37 Expected mean rata of impingement losses of bay anchovy. 6.2-38 Expected mean rate of impingement losses of weakfish. ( _ --- - - - - l
Salem 316(b) Demonstration Number Title 6.2-39 Summary of estimated annual impingement losses at Salem Generating Station under various plant operating conditions. 6.3-1 Blueback herring conditional impingement mortality rate using the best estimates of population size and instanta-neous daily mortality. 6.3-2 Alewife conditional impingement mortality rate using the best estimates of population size and instantaneous daily mortality. 6.3-3 American sbad conditional impingement mortality rate using the be;st estimates of population size and instanta-neaus daily tLortality, 6.3-4 Computation of equivalent adults for projected spot i ' entrainment losses. 6.3-5 Computation of equivalent adults for projected spot impingement losses. l f 6.3-6 Summary of equivalent adult losses of spot due to entrain-ment and impingement under typical full operation for various
' - outage schedules.
6.3-7 Summary of reported and calculated daily instantaneous mortality rates of spot 0+ (juveniles) for various locations along the mid-Atlantic coast. , 6.3-8 Spot 0+ conditional impingement mortality rate using the best estimates of population size and instantaneous daily mortality. 6.3-9 Spot 1+ conditional impingement nortality rate using the best estimates of population size and instantaneous daily mortality. 6.3-10 Summary of spot 0+ and 1+ conditional mortality rates under typical full operation for various outage schedules. 6.3-11 Striped bass age-specific survival probabilities. 6.3-12 Instantaneous total mortality rates for Neomysis americana based on length-frequency data, estimated growth rate, and calculated median life span r'uring 1979-1980. 6.3-13 Estimated' median life span of Neomysis americana based on stable age distribution.
Salem 316(b) Demonstration Number Tit . 6.3-14 Summary of model input parameters and calculated exploitation rate for Neomysis americana. 6.3-15 Instantaneous total mortality rates for Gammarus spp. based on length-frequency data, esticated growth rate, and calculated median life span during 1979 and 1980. 6.3-16 Estimated median life span of Gammarus spp. based on stable age distribution. 6.3-17 Summary of model input parameters and calculated exploitation rate for Gammarus spp. 6.3-18 Estimated instantaneous mortality rates for white perch. 6.3-19 khite perch conditional mortality rate, as calculated using E1MODEL 2, with best estimate of population size mortality rates. 6.3-20 Summary of conditional mortality rates, lost reproduct ive po:.entials , and productions foregone computed for white perch under various outage schedules. 6.3-21 Bay anchovy age-to-stage conversion matrix. O 6.3-22 Bay anchovy spawning fraction by week (R-factor) and annual egg production for 1979 through 1982. 6.3-23 Bay anchovy juvenile / adult wcekly impingement F-factor. 6.3-24 Bay anchovy W-factor by life stage and length interval. 6.3-25 Weekly D-factor for bay anchovy 0+. 6.3-26 Weekly D-factor for bay anchovy 1+ and older. 6.3-27 Summary of conditional mortality rates for bay anchovy 0+. 6.3-28 Summary of conditional mortality rates for bay anchovy 1+. 6.3-29 Mortality rates of engraulid eggs, larvae, and adults. 6.3-30 Growth rates for Delaware Bay larvae, juvenile, and adult (0+ and older) bay anchovy generated from literature values and data from the present study. 6.3-31 Summary of conditional mortality rate and production foregone for bay anchovy 0+ through 3+ under various outage schedules.
Sales 316(b) Dtmonstration Number Title 6.3-32 Weakfish age-to-stage conversion matrix. 6.3-33 Weakfish egg recruitment, by week, and annual egg production in the Delaware River estuary, based on egg standing crop estimates adjusted for incubation time. 6.3-34 Weakfish W-ratio by life stage. 6.3-35 Weekly D-factor for weakfish. 6.3-36 Summary of conditional mortality rates for weakfish. 6.3-37 Sumcary of weakfish daily instantaneous mortality rates by stage. 6.3-38 Summary of conditional mortality rate and production fore-gone computed for weakfish under various outage schedules. O U
Salem 316(b) Demonstration O LIST OF FIGURES: SECTION 6 Number Title 6.1-1 Density of Atlantic croaker larvae observed in entrainment and River samples, 1977-1982. 6.1-2 Density of Atlantic croaker juveniles observed in entrainment and River samples , 1977-1982. 6.1-3 Striped bass density near Artificial Island. 6.1-4 Observed and predicted entrainment density of white perch prolarvae at Salem. 6.1-5 Observed and predicted entrainment density of white perch postlarvae at Salem. 6.1-6 Observed density of bay anchovy eggs in entrainment abundance s amples , 1977-1982. , 6.1-7 Observed density of bay anchovy larvae in h entrainment abundance sampir.s, 1977-1982. 6.1-8 Observed density of bay anchovy juvenile / adults in entrainment abundance samples, 1977-1982. 6.1-9 Observed and predicted entrainment density of weakfish eggs at Salem. 6.1-10 Observed and predicted entrainment density of weakfish prolarvae at Salem. 6.1-11 Observed and predicted entrainment density of weakfish postlarvae at Salem. 6.1-12 Observed and predicted entrainment density of weakfish 0+ (juveniles) at Salem. 6.1-13 Comparison of entrainment abundance and adjusted river density estimates of Neomysis americana. 6.1-14 Comparison of entrainment abundance and adjusted river density estimates of Cammarus tigrinus group. O
Salem 316(b) Demonstration Number, Title 6.3-1 Relationship among the terms "entrainment period,"
"entrainment interval," " time step," " cohort," and
" spawning periods." (Boreman et al. 1978).
6.3-2 Estimation of production in the production foregone analysis (Pitcher and Hart 1982). 6.3-3 Summary of input parameters for ETM. 6.3-4 Summary of input parameters for EIM. 6.3-5 Spot 0+ mean densir.y, by collection period, during 1979 and 1980. 6.3-6 Spot 1+ and older mean density, by collection period, during 1979 and 1980. 6.3-7 Segmentation for each regionof(1,000 the study)m . area in the ETM and volumes O O
4 Salem 316(b) D:monstration SECTION 6: i ENTRAINMENT AND IMPINGEMENT Section 6.1 describes the entrainment of aquatic organisms at the Salem Generating Station based - on data collected during 1977-1982. A descrip-tion of the Lapingement of fish species during the same period follows in Section 6.2.' .In Section 6.3, the entrainment and impingement losses for the target species are related to information regarding their River populations. The equivalent adult, conditional mortality rate, produc-tion foregone, _ and lost reproductive potential approaches are used, either alone or in combination, for the target fish species depending on the biology of the species and the information available. For the two 4 macroinvertebrate taxa, the exploitation rate approach is used. 6.I'-ENTRAINMENT
! .6.1.1 TliE ENTRAINMENT PROCESS AND TARGET SPECIES When cooling water is withdrawn from a source waterbody, small biolog-ical organisms in the waterbody are drawn into the plant along with the cooling water. This process is known as "entrainment." The degree of susceptibility to entrainment usually depends on the size and mobility of
-these organisms and their distribution relative to the station intake.
4 - At Salem station, entrainment occurs primarily in the circulating water
. system'(CWS) and, to a much lesser degree, in the service water system (SWS). These systems are described in Section 3.3.
Upon passage through the CWS, organisms may be subjected to thermal, mechanical, and' chemical stresses. Their ability to withstand these stresses varies from species to ' species. Therefore, species-specific
'entrainment survival. rates must be considered in assessing entrainment l.
losses associated with CWS. operation. At the SWS, the relatively small number of entrained organisms are assumed not to survive. I IDa obtain the data needed to determine the potential ef fects of entrain-ment at Salem, the entrainment monitoring program was conducted from
' August 1977 through October 1982. This program is described in Section 4.3.1. Its main objectives were to estimate (1) the abundance of organisms that - passed through the Salem CWS, and (2) the survival of entrained organisms.
As detailed in Section 3.3, 9.5-mm mesh traveling screens are installed at both the circulating and service water intakes of the Salem station. The maximum size of entrainable organisms is limited to those that can pass'through.the intake screen. Entrainment of fish species usually involves only the early life stages of eggs, larvae, and juveniles. Other organisms, 'such as microzooplankton and macroinvertebrates, may be IJ f susceptible to entrainment throughout their life span because of their small size. 6.1-1
Salem 316(b) Demonstration Entrainment of aquatic organisms is also af fected by their mobility, g Eggs are passive and are therefore entrained in proportion to their occurrence in the intake withdrawal zone. On the other hand, larvae and juveniles may exhibit behavioral patterns that will either increase or reduce their chances of being entrained. The single most important factor influencing the entrainment of any given species is when entrainable life stages occur in the vicinity of the station. This, in turn, is related to how the Delaware estuary is used by the different species. The life history summaries for the 11 target species, summarized in Section 5 and detailed in Appendixes II-XII, are used below to predict the potential exposure of each species to entrain-ment by Salem station. Exposure is defined here as the presence of a species in the intake area. Therefore, it indicates the possibility of that species being cropped by the station. Detailed analyses of Salem's effect on each species are presented in Section 7. Bay anchovy is an abundant , small (<120 m:t) forage species that uses various regions of the Delaware estuary throghout the year. The spawn-ing season is protracted, extending primarily trom May through August. Spawning occurs throughout Delaware Bay and , to a lesser extent, in the lower Delaware River. Bay anchovy occur near Artificial Island during most of the year and are typically abundant from April through November. Thus, bay anchovy are exposed to entrainment by Salem station. Weakfish enter the Delaware estuary as adults to spawn in the spring and summer. The spawning season extends primarily from late May through August. Most spawning occurs between the mouth of the Bay and Woodland Beach (rkm 64), with relatively low densities of eggs found in the vicinity of Artificial Island. Af ter hatching, larvae move to nursery areas in the upper Delaware Bay and lower Delaware River. Young weakfish (20-35 mm) are found in the vicinity of Artificial Island typically from mid-June through August at densities lower than those of bay anchovy. Weakfish also grow rapidly; therefore, their entrainable period is relatively short. Based on this life history information, the potential exposure of weakfish to entrainment at Salem is not as high as that for bay anchovy. White perch spawn mostly in the Delaware River between Newbold Island and Trenton with little spawning activity in the Artificial !sland vicinity. White perch eggs are adhesive, and therefore occur in the Artificial Island area only during very high river flows. The principal nursery area for larvae is somewhat downstream from the spawning area but still well upriv'er from the Artificial Island area. There fore , white perch entrainment exposure is very low. The three clupeid species (blueback herring, alewife , and American shad) are all anadromous species that enter tue Delaware estuary during annual spawning runs. Most of the spawning takes place well upstream frem Artificial Islaid. Young generally remain upriver until f all when they start their seas ard migration. Therefore, young clupeids are relatively abundant near A:tificial Island for a short period of time and their exposure to entrainment is low. 6.1-2
. , .- - . _ - - - - . . ~. . - _ _ _
Salem 316(b) Dzmonstration N 1 Spot spawn offshore -along the Atlantic coast during late fall through s j'
' early spring. ' Af ter hatching, larvae and -juveniles mete inshore to the estuarine nursery areas, primarily in the tidcl- creeks and marshes.
Young ' spot- appear abundant in the Delaware only when large year-classes ificial are produced offshore. - Curing such years, their abundance near ArtSpot are t 7 Island is greatest during late spring and fall.The relative abundance data . indicate the fall to be entrained.'et'to entrainment is~1ower than bay anchovy and potential exposure o' ar than other fish species. weakfish, but.may be Atlantic croaker, similar to' spot, spawn offshore. Larvae migrate 4 into -the . estuary during fall and move quickly to the upriver nursery p As growth proceeds, the larvae gradually move downstrean toDuring late f areas. higher salinity areas, including the Artificial Island area. Decem The population of Atlantic
' as the fish start their seaward migration.
creaker young-of-the year in the -Delaware fluctuates widely from year to ! year._ Consequently, entrainment' of Atlantic croaker, restricted to che fall and early winter months, is expected to vary considerably on an annual basis, f- ~ Striped bass use large river systems such as the Delaware River asH spawning and nursery habitat. dd l
~
~
;of ~ the Delaware system has been greatly reduced as a result of water quality and habitat. -
;(
5 year are found in the Delaware, and these areTherefore, apparently the -the result of
~.
Ji spawning in the Chesapeake. and Delaware (C&D) Canal ' . low. Neomysis americana is the most common and abundant mysid ~ in the Delaware Maximum abundance occurs from June through November or December ' estuary. Because of its small size, N. Americana is at salinity _ of ~ 15-20 ppt . ~ Since N. Americana
. susceptible to entrainment throughout its life' span. i nt by Salem is abundant throughout the -Bay, it is- susceptible to entra nme
!? station. The Gammarus tigrinus group consists of three species and occurs in the l- LDelaware estuary mainly is ~intypically the region abundant of.rka from64-117, March throughwhich includes the It [- ArtificialzIsland area. Because .of their small size, organisms in- the Gammarus group are August. Since they are l-susceptible to entrainment during their entire life hAspan.st,^they are exposed to
. abundant in the ' station vicinity during Marc - uguHowever, the abundance of E
entrainment primarily during this period. Consequently, entrainment this. group is lower than that of N. Americana. f N_. Americana.
- of Gaasnarus is -also expected to be lower than that o
/
i
'6.1.2 ENTRAINMENT DENSITIES 1.
5The methods-used to esdinate entrainment Sectiondensities, both observed a 6.1.2.2 presents
/~'[ projected , 'are introduced in Section 6.1.2.1. Salem.
F A~-{ L [" the onsite entrainment' data collected from 1977.throu 6.1-3
Salem 316(b) Demonstration f acility operations from entrainment observations during previous opera-tions. River abundance data were used in co 2 junction with onsite data to estimate entrainment densities as appropriate. -action 6.1.2.2 concludes with a summary of the projected entrainment denst ies for each target species. 6.1.2.1 Methods Used to Estimate Entrainment Densities The onsite entrainment abundance program, initiated in August 1977, was conducted through October 1982. Up to June 1980, from 8 to 12 samples were taleen during each sampling period, which lasted 1-2 days. Subsequently, approximately four samples were taken during each sampling period. (The sampling program and schedule are described in rore detail in Section 4.3.1.1.) Mean entrainment densities for each sampling period were computed by life stage for each species by averaging the entrainment densities computed for each sample collected. The mean densities and confidence intervals by sampling periods for each target species are presented in Section 6 of Appendixes II-XII. A more detailed dia< nasion of the computation of observed entrainment densities and their confidence intervals is provided in Section 2 of Appendix 1. Projected entrainment densities of the target species under future conditions can be estimated from enree different methods, one calculated directly from observed onsite entrainment data, another from river abundance data collected in the vicinity of Artificial Island , and a third from combinations thereof. The projected weekly densities were then calculated as the unweighted mean of all observed values during each weekly period. Linear interpolation was used to derive estimates of weekly values between data points. For several target species--including Atlantic croaker, striped bass, N_. americana, and Gartmarus spp.-- onsite entrainment data alone were considered inadequate to project future entrainment densities. Onsite entrainment abundance sampling was infrequent during the peak abundance periods of Atlantic croaker and striped bass. In addition, these two species are present at low abundance in the River, and consequently are entrained only sporadically by the station. Therefore, river abundance data for Atl~ antic croaker were adjusted for gear efficiency and combined with the onsite entrainment data to establish a more representative database. The combined data were then used to compute the projected entrainment densities , using the same methodology described previously. The actual river and casite abundance data used in the computation are presented in Section 6.1.2.2. For striped bass, the onsite entrainment data are too sparse, since only two striped bass eggs were collected during the 1977-1982 sampling period. Therefore, only the river abundance data, unadjusted for gear efficiency, were used to estimate entrainment densities.. No adjustment was made to account for gear efficiency, because striped bass are present as eggs and yolk-sac larvae with little, if any, demonstrated ability to g avoid gear collections. W 6.1-4
Szicm 316(b) Demonstration
/~) For the two macroinvertebrate taxa, N. americana and Gammarus spp.,
k/ onsite entrainment sacpling was conducted only from 1977 through 1980. Except for 1980, the onsite entrainment data are sparse. Since 1980 represents only a single (and perhaps unusually dry) year, projections based solely on these data tre not appropriate. For these two taxa, the long-term eiver abundance data (1974-1980) near Salem were adjusted using the less avoidance-af fected onsite entrainment data by first calculating seasonally weighted ratios of entrainment vercus River densities. These ratios were then applied to adjust the monthly mean River densities from 1974 to 1980 to estimate the projected entrainment densities. The actual computations for these two taxa are presente'd in Section 6.1.2.2. 6.1.2.2 Estimated Entrainment Densities This section first presents the observed onsite entrainaent data for macroinvertebrates during 1977-1980 and for ichthyoplankton during 1977-1982. The projected entrainment under future plant operation is then estimated from these observations. Analogous data are presented for those species for which the projection is based on river abundance data. Observed Entrainment From 1977 through 1982 Entrainment of macroinvertebrates was measured for all species during j 1977 and 1978 and for the two target taxa (N. americana and Gammarus spp.) from 1977 through 1980. The rank and percentage of total catch of / ("] all macroinvertebrates in 1978 are shown in Table 6.1-1. Since only two (/ collections were made in 1977, the rank and species composition were not summarized for that year. According to the 1978 data, only a few species ! constituted a large fraction of the total macroinvertebrate entrainment. The four most abundant taxa (N. americana, Rhithropanopeus_ harrisii, Gammarus spp. , and Edotea triloba) together made up 96.7 percent of the total annual entrainment catch. Of the 58 taxa identified, 45 consti-tuted < 0.1 percent of the total entrainment. Neomysis americana was, by far, the most abundant macroinvertebrate l entrained . in 1978 (Table 6.1-1), constituting 81.6 percent of the total entrainment catch. It was entrained during each month of sampling, although the degree of involvement depended on the season. Highest entrainment densities are normally observed during early summer and early fall. l l Rhithropanopeus harrisii, the mud crab, was the second most abundant macroinvertebrate entrained, constituting 11.2 percent of the total entrainment in 1978. It occurred from April through December, with peak densities from June through mid-August (PSE&G 1980). Gammarus spp. comprised three species, G. fasciatus, G. daiberi, and G. tigrinus, and ranked third among all macroinvertebrates entrained in 1978, only 2.2 percent of the total. It was entrained during all months of sampling, with the highest densities observed during spring /
~'% early summer.
(O 6.1-5
Salem 316(b) Demonstration As discussed in Section 4.1, N,. Americana and Gammarus were selected as two of the target species for this 316(b) Demonstration. Entrainment lh data for these taxa were collected over the 1977-1980 period. Table 6.1-2 presents entrainment densities for these taxa for each sampling period. Table 6.1-2showsJunethroughOctoberastheperiogofgreatest entrain-ment for N. Americana. Peak densities were 776.9/m on September 3 13-14 in 1978, 668.0/m' on October 17-18 in 1979, and 798.0/m on June 22-23 in 1980, respectively. Entrainment densities from November through May were generally much lower. l Gammarus spp. was entrained throughout the year; the period of greatest density was from Agril through mid-September. Pegk entrainment was observed at 16.lfm on June 28-29 in 1978, 31.1/m on July 25-26 in 1979, and 51.7/m on April 16-17 in 1980. Entrainment densities from mid-September through March were very low. In comparison with N. Amer-icana, the entrainment densities of Gammarus spp. were generally lower by an order of magnitude. Entraincent of ichthyoplankton at Salem was studied from 1977-1982. The 1977 data were limited to only two sampling dates and were not analyzed for species composition. In 1982, entrainment data were analyzed for all species through July, but for only the three primary species from August through December. Therefore, the 1982 entrainment data were not considered in the species composition. Table 6.1-3 presents the species g composition of ichthyoplankton by year and the composite species composi-tion during 1978-1981. Bey anchovy was the dominant entrained species for all life stages (Table 5.1-3). This was particularly apparent for bay anchovy eggs, which constituted 99.3% of all entrained eggs from 1978 through 1981. Eggs of mine additional taxa were identified from the entrainment collections. Each accounted for 0.4 percent or less of the total entrainment. Bay aechovy had a 4-year average of 76.8 percent of total entrained larvae. Averaged over 1978-1981, four taxa constituted at least 1.0 percent of the entrained larvae: gobies (17.0 percent), silversides (2.5 percent), weakfish (2.1 percent), and hogchoker (1.1 percent). Of the other identiiied Isrvae entrained (12 taxa), each formed less than 0.1 percent of the total abundance. Overall, 0.3 percent of the larvae could not be identified. Twenty-two taxa of young fishes were identified in entrainment collec-tions during 1978-1981; less than 0.1 percent could not be identified. Young bay anchovy (Table 6.1-3) accounted for 69.3 p'ercent , ranging from 54.1 percent in 1979 to 79.3 percent in 1980. Weakfish was the second most abundant species, accounting for 13.7 percent of all young fish entrained during 1978-1981. Seven taxa each formed more than 1.0 percent of the 1978-1981 entrainment abundance. Some adult fishes were entrained during 1978-1981, the most abundant being bay anchovy (96.7 percent of lll all entrained adults). Each of the other eight taxa of adults consti-tuted less than 1.0 percent of the total adult entrainment. ( l 6.1-6
Salem 316(b) Demonstration
/) Table 6.1-4, the entrainment data for fish eggs during 1977-1982, shows \' ' that except for bay anchovy and, to a lesser degree, weakfish, eggs of most target species are either not entrained or are entrained in low densities. Bay anchovy eggs are entrained primarily during the summer, with peak densities occurring during July. However, taan density varied annually, with highest monthly densities observed during the summers of 1979 and 1980. Relatively low densities were seen in 1982.
Weakfish eggs were entrained from May through August at low densities. The other two target species whose eggs were entrained during 1977-1982 were white perch and striped bass. For these species, entrainment was also sporadic , occurring over a period of one. month fe r both white perch and striped bass. Eggs of the other target species were not observed in entrainment collections. The eggs of most of the target species were not subject to entrainment. This is to be expected in view of the life history patterns of the species involved (Section 5). For example, Atlantic croaker is an ocean spawner. Its eggs are shed offshore and are found a considerable distance from Salem. I Some eggs of nontarget species were also entrained at Salem, primarily l during spring and summer months, but usually at low densities (Table 6.1-4). Silverside eggs were the most abundant among the nontarget species. , /N f(- Entrained fish larvae consisted mainly of bay anchovy (Table 6.1-5) and, to a lesser degree, weakfish. The other target species were entrained only sporadically (white perch and Atlantic croaker) or not at all (blueback herri g, American shad, alewife, spot, and striped bass). Larvae of ind *.vidual nontarget species were collected at relatively low densities during most months sampled. Bay anchovy larvae were entrained frut late spring through the fall, with monthly densities peaking in July of each year. Entrainment density declined by late summer /early fall, indicating a relatively short period of maximum entrainment involvement. This may be attributed to rapid growth and the movement of this species out of the vicinity. During the July geak entrainment , maximum densities were 6.1, 5.9, 24.2, 10.7, and 5.1/m in 1978, 1979, 1980, 1981, and 1982, respectively. Weakfish larvae, the second most abundant entrained target species,
. were collected mainly during tge late spring / summer. Densities reached a maximum (up to 0.7/m ) in July of each year. The period of entrainment for weakfish larvae was more limited than that for bay anchovy.
White perch and Atlantic croaker larvae were the only other target species entrained. For these species, larval entrainment was restricted to one to tnree months; in some years no larvae were entrained. The I') remaining target species (blueback herring , American shad , alewife , spor ,
and striped bass) were not identified in entrainment collections. La rv+ e of nontarget species were entrained at Salem from spring through fall, 6.1-7
Salem 316(b) Demonstration with peak entrainment occurring during the summer. Gobiosoma spp. and lh silversides dominated the larval entrainment of nontarget species. Entrainment samples of juvenile fishes (Table 6.1-6) indicated that seven of the nine target species were entrained at Salem; no American shad or striped bass juveniles were entrained. A variety of nont arget juveniles were also entrained during each year of station operation. Of the juveniles collected, bay anchovy was the moat abundant species of that life stage. Entrainment occurred each year tuting spring through fall. Weakfish juveniles were also abundant in e~trainment collections, primarily during the summer and early f all. Spot j uveniles were also entrained each year, chiefly during late spring /early summer. Juveniles of other target species (white perch, blueback herring, ale-wife, and Atlantic croaker) were entrained in only some years of sam-pling. For example, white perch juveniles were collected only during December 1977. Blueback herring juveniles were taken during November 1978, March, May, and June 1980, and May 1981. Alewife juveniles were taken only during April and May 1980. The year-to-year variation may reflect the low densities of these species in the plant vicinity as well as the infrequent sampling schedule during their period of peak abun-dance. American shad and striped bass j uveniles were not identified in entrainment collections. For the clupeids, some juveniles , identified only as Alosa spp., were also collected in entrainment abundance samples during 1560 and 1981. Judging from the early timing of the Alosa spp. h peak, these may have been predominantly alewife. Some species , e .g. , bay anchovy, that reach maturity at a small size have been entrained at Salem (Table 6.1-7). Adults of some larger species, such as American eel, have also been entrained because of their fusiform shape. These two species were entrained as adults--mostly, however, at low densities in comparison with larval and juvenile entrainment (Table 6.1-7). Projected Entrainment Densities Entrainment densities for several target species under future station operation can be projected from the onsite entrainment densities observed during 1977-1982. The projected entrainment densities were estimated by computing the unweighted mean of all observed entrainment data from 1977 through 1982 in weekly intervals. This procedure was applied to project entrainment densities for spot , blueback herring, alewife , and American shad. For other target species, the observed entrainment data were too sparse by themselves to determine their involvement with Salem station. Atlan-tic croaker larvae, for example, are typically entrained during late September through early November, while juveniles are entrained during late October through early December. As shown in Table 6.1-5, relatively little entrainment sampling was conducted at these times because of icing h problems. Therefore, to increase sample size and provide broader tem-poral coverage, the river sbundance data of entrainable croaker near 6.1-8
Esism 316(b) Damonstration
' Artificial . Island were also used in conjunction with onsite entrainment data, he river abundance data were adjusted based on estimates of gear efficiency from the literature. As reported by LMS (1980), efficiency of a 1-m plankton net was estimated to be 45 percent for croaker 6-20 mm SL and 15-30 percent for croaker 21-25 mm. Since a 0.5-m plankton net was used in this study program, the low estimates of collection efficiency (45 percent for specimens _(20 mm and 15 percent for those >20 mm) were adopted. He onsite and river data used to estimate the projected entrainment densities for Atlantic croaker larvae and juveniles are presented in Figures 6.1-1 and 6.1-2, respectively.
For striped bass, the onsite entrainment data indicate that only two eggs were taken (in one sampling period on April 19-20, 1978) from 1977 through 1982. No striped bass larvae or juveniles were taken in the onsite entrainment program. River data indicate that striped bass eggs and larvae, probably the result of spawning in the C&D Canal, can be
. expected in the Artificial Island region during April and May. As shown in Table 6.1-4, onsite entrainment sampling during these months was probably insuf ficient to determine actual levels of involvement of l striped bass early life stages, which typically occur sporadically and at l low densities in this area. In lieu of theae data, entrainment densities j -were projected from the river abundance data collected between rkm 64-97
- f. from 1975 to 1980 in the present study. Figure 6.1-3 presents the river abundance data for striped bass eggs and larvae using a 0.5-m plankton net during 1975-1980; no -striped bass juvenilee were collected. Pro-
'p ' jected entrainment densities for striped bass eggs and larvae were ' 'V - calculated. as the unweighted mean of the River densities (unadjusted for
,f collection efficiency) on a weekly basis. For white perch, entrainment occurs. typically during April-June, a period during which onsite entrainment sampling data alone were judged insuf fi-cient. Herefore, the projected entrainment densities for white perch were obtained by combining the onsite entrainment ' data during 1977-1982 with the density estimates from the 0.5-m plankton net sampling in the Delaware River near Artificial Island (rka 64-97) for the same period.
' Within each 7-day period, beginning January 1, density values from either data: set were averaged as an unweighted arithmetic mean to yield project-ed mean weekly densities. he 0.5-m plankton net data were not adjusted to account for gear avoidance since 'such values could.not be generated from present-study data nor are they available in the literature.
Figures 6.1-4 and 6.1-5 present the onsite entrainment data and the 0.5-m
; plankton net data as well as 'the projected entrainment densities for pro-and postlarvae of white perch. Because white perch typically spawn well upriver of Sale'a, or up tidal tributaries, and their eggs are adhesive, it was' expected that few eggs would be entrained.
his is borne out by the fact that only two eggs were taken in entrain-ment samples during-1977-1982 and only seven eggs were taken in ~ 0.5-m plankton net samples in the rkm 6'+-97 region over the same period.
.Because of their sporadic occurrence at low density and their improbable
[ involvement with ' Salem, projections of entrainment densities for white A - perch eggs were not considered justifiable or necessary. 6.1-9
A Salem 316(b) Demonstration For both bay anchovy and weakfish the 1977-1982 onsite entrainment database provides a source from which reliable estimates of projected densities for each life stage can be generated. The unweighted mean of all observed values was calculated for each life stage by weekly interval beginning January 1. Figures 6.1-6 through 6.1-8 present the observed and projected entrainment densities for bay anchovy; Figures 6.1-9 through 6.1-12 present these densities for weakfish. For the macroinvertebrate taxa N,. americana and Gammarus spp., neither the entrainment abundance data nor the river abundance data are entirely suitable for estimating entrainment densities. The onsite data were collected only from 1978 through 1980 and, except possibly in 1980, were too sparse. The river abundance data, while covering the period from 1974 to 1980, were biased by gear avoidance, especially during the warmer , peak-abundance months. Therefore, entrainment densities were estimated by scaling the long-term river abundance data to the less avoidance-affected entrainment data. This was accomplished by first calculating seasonal ratios of entrainmant vs. river (E/R) densities from the corresponding sets of data in 1979 and 1980. These E/R ratios were then used to adjust the mean monthly river abundance between rkm 64-97 from 1974 to 1930 to project future entrainment. Table 6.1-8 presents the 1979 and 1980 N. americana entrainment and river abundance data used in the computation of the E/R ratios. Only those samples from both localities that were separated by two days or less were selected. Analysis of this database suggests that on corre-sponding dates, densities in Salem intake water samples were, on the average, 3.75 times greater than densities found in the Delaware River water samples. A paired t-test indicated that the probability of a difference of this magnitude aris3ag from chance alone was less than
< 1 percent (t = 3.676; df = 25; p i 0.01). The seasonal ratio of entrainment/ River density for November through April was calculated to be 0.857 and 3.843 for May through October. These ratios were then used to adj ust the monthly mean river sample densities from 1974 to 1980 (Table 6.1-9) to obtain estimates of projected entrainment densities. The adjusted values appear to give a reasonable fit to the observed entrain-ment densities (Figure 6.1-13) .
The 1979 and 1980 entrainment and river abundance sampling data and the computed density ratios for Gammarus spp. are presented in Table 6.1-10. Densities in the Salem intake water samples were on the average 6.37 times greater than in the Delaware River water samples. A paired t-test indicated that the probability of a dif ference of this magnitude arising from chance alone was < 0.1 percent (t = 4.54; df = 25; p 10.001) . The seasonal ratio of entrainment/ River density for November through April was calculated as 3.643 and 9.018 for May through October. These ratios were used to adjust the densities of monthly mean river samples from 1975 to 1980 to obtain estimated entrainment densities (Table 6.1-11). These adjusted values appear to give a more conservative (i.e . , higher) estimate of entrainment abundance than would result from onsite entrain- g ment data (Figure 6.1-14) . W 6.1-10
-.i.-..
>. 8 h 5' O IMAGE EVALUATION /jjf/ j I$ 4p [*s,>pk h@ ' TEST TARGET (MT-3) Y / , Q sfg,#, 4 p' W <% , l.0 'd En Na DE j,l 5 *lfIl!il==iis E { l.8 1.25 1.4 1.6 4 150mm >
< 6" >
l~bkY,><? *) ?k% :.
?.+4 c ;
L% - - -
4> #<> o o IMAGE EVALUATION f [gI*4, (([NT jt #4 f '4 g pf7 y@y i TEST TARGET (MT-3) pf'
$pV k"p, ,,f4?
+ %
l.0 'd m BE
;gj m
. i,i [' Ne 118 l.25 l I.4 1.6 I 5 < 150mm >
< 6" >
=
# /+4 % %y %,,,8,, , <g(b si, \
t~~ _. . v
Salem 316(b) Demonstration
]) Based on tue methods described above, the projected entrainment densi-ties for each target species were calculated on a weekly basis and are summarized in Tables 6.1-12 and 6.1-13 for the secondary and primary target species, respectively. These projected densities are later com-bined with. the entrainment survival rate and plant withdrawal volume (Section 6.1.4) to estimate the rate of entrainment losses under future plant operations for each target species.
6.1.3 ENIRAINMENT-SURVIVAL RATES
- Entrained organisms experience mechanical buf feting and abrupt changes in temperature and pressure during their passage through the cooling water system. Additionally, during the period of chlorine application organisms also experience biocidal ef fects. Although some organisms may sustain injury or die, others survive the stresses involved. There-fore, to estimate- the rate of entrainment losses for each target species, the estimated densities must be adjusted by the entrainment survival rate for that species.
In this study, computation of entrainment survival rates incorporates both initial and latent ef fects. Initial mortality is defined as the death of an organism during entrainment. Latent mortality is defined as survival of the actual passage through the generating plant but subse-quent death caused by earlier injuries or stress during entrainment. To measure the latter component of entrainment mortality, live and stunned I) organisms were held in aquaria and observed for a standard period of time
' after entrainment to determine the percentage of initial survivors that
'would later succumb to these stresses. The observation period was chosen based on the combined experience of scientists from the Technical Advisory Group (TAG) and PSE&G's consultants. Mortality caused by this holding procedure is, in turn, determined by placing organisms collected at the intake in identical conditions and observing their fate.
' The potential for entrained organisms to survive is not only species-specific but also age-specific. Section 6.1.3.1 describes the methods used to estimate entrainment survival rates. The estimated rates for each' target species are presented in Section 6.1.3.2. These survival rates are applied in Section 6.1.4 in conjunction with entrainment densi-ties and station flow rates to estimate the rate of entrainment losses.
6.1.3.1 Methods Used to Estimate Entrainment Survival Rates Two independent studies--onsite studies using intake and discharge samples and laboratory simulation studies--were conducted to estimate entrainment survival rates for the target species. In general, the onsite studies evaluated the nonthermal mortality whereas the simulation study evaluated the thermal mortality. Although the two studies dif fer in what they measure, and each has its own sources of bias, their results L can be used in conjunction with available literature values to derive
-~ .
reasonable estimates of total entrainment survival rates. 6.1-11
- - -, - _ . _ _ . _ . - __ _ _ .. . _ _ _ ~ _ _ _ _ _ _ . _ _ _ _ _ _ .
Salem 316(b) Demonstration Onsite Studies Onsite entrainment survival studies were conducted by comparing the survival rates of intake samples (control) versus discharge samples (experimental) collected using either the larval table or low-velocity flume methodology. The larval table (Figure 5.1-11), used in 1977-1980, r ef fectively3) size (3-7 m was educed collection-induced not large mortality; enough to produce however, sufficient its sample specimens for statistically meaningful results. Therefore, in 1981 and 1982, entrain-ment survival samples were collected using the low-vglocity fiume (Figure 5.1-12), which increased sample volume to about 75 a without substan-tially increasing collection-induced mortality. During 1977 and 1978, entrainment survival sampling was scheduled twice per month from June through August and once per month from September through May. During 1979 and 1980, the schedule was the same, except that sampling frem December through February was eliminated. During 1981 and 1982, the sampling schedule was intensified: four times each in June and July, twice each in May and August , and once each in September and October. However, because of plant outages, samples could not always be collected. A detailed description of the experimental design and execu-tion of the onsite studies is, presented in Section 5.1.2 of Appendix 1. After collection, the entrainment survival samples for ichthyoplankton and macroinvertebrates were examined for initial mortality. Organisms were categorized according to the following criteria:
- 1. Live--swimming vigorously, no apparent orientation problems, behavior normal
- 2. Stunned--swimming erratically, struggling, or swimming on side, some twitching but motile
- 3. Dead--no vital signs , no body or opercular movement ,
no response to gentle probing Live and stunned organisms were placed in separate holding tanks fo r latent mortality observations for up to 12 hours in 1977-1978 and 96 hours in 1981-1982. Estimations of total entrainment mortalities are derived based on the equation developed by Abbott (1925): f=1 D- (Equation 6.1-1) I where f = fraction of live organisms entering the intake estimated to be killed by plant passage D =. discharge survival rate I = intake survival rate 6.1-12
, , Salem 316(b) Demonstration When the onsite survival data were limited to those collected at dis-
- charge temperature < 30*C, the temperature below which thermal responses
- l. - are not likely to be induced, the mortality rate computed using Equation i- 6.1-1 was used to represent the nonthermal mortality.
Entrainment Simulation Studies Entrainment simulation studies were conducted in the laboratory to.
. determine the potential mortality of entrained organisms attributable
, to specific components of stress caused by increased temperatures and ! changing pressures or their synergistic ~ effects. Each simulation study i included both the control and the experimental samples. The former , received no handling or testing' stresses, and reflected only natural and holding-system-related mortality. - The experimental samples were subjected to different combinations of pressures and temperature rises
- representative of passage through the CSS. The' experimental design and i execution of the entrainment simulation studies are described in Section i 5.1.3 cf Appendix I. .
The data obtained 'from the entrainment simulation studies were analyzed 4 using the multiple probit regressio~n methodology, a detailed description of which is presented in Appendix I, Based on the results of onsite and simulation studies, and using lit-
~
erature reported values for comparisons, the nonthermal and thermal mortality rates were evaluated separately. The nonthermal mortality rate
.^O included . the effects of mechanical and chemical stresses. The total entrainment mortality rate was then computed based on the following equation:
M = 1 - ( 1 - M,) x ( 1 - Mt ) (Equation 6. b2) T b
. where M = total entrainment mortality rate T
M,-= nonthermal mortality rate M g = thermal mortality. rate 6 .1'. 3. 2 Estimated Entrainment Survival Rates The entrainment survival rates for each target species were estimated
. from the results of onsite 'and simulation studies. Whenever possible,
, these results were also compared with the reported values from other
- waterbodies. Based on these conparisons, the most realistic estimates
- of the survival rate were selected.
' - Detailed 'information regarding the entrainment survival data and their analysis is presented in Section 6 of each species-specific report.
~
- - Estimated entrainment survival rates for each target species and a brief discussion of how they-were' derived are sununarized below.
= 6.1-13
,,.+.....-r,.r.-.- ,,,--,.---,--,,-v.,.,,- ~~,,,.v,~-'.m..e-,--.-.v1,--.,-.,,..---r,..,-w,,e.~,e,,,.,. . e--,--e.-, .m ..,---
Salem 316(b) Demonstrttion Spot Nonthermal mortality of early juvenile spot was calculated from onsite entrainment survival data at discharge temperatures below 30*C. Survival of 130 spot collected at the discharge was 74.1 percent, while survival of 66 spot collected concomitantly at the intake was 90.9 percent. Substituting these values into Equation 6.1-2 yields a nonthermal en-trainment mortality of 18.5 percent. This value agrees well with the value of 25 percent reported at the Brunswick station on the Cape Fear, Ncrth Carolina (Jinks et al. 1980) and 18 percent at the Calvert Cliffs station on Chesapeake Bay (EA 1979). The effect of chlorination can be factored into the nonthermal mortality by assuming 100 percent mortality of entrained organisms during periods of chlorinat an. Since chlorina-tion is scheduled to occur for three 30-minute periods each day, the ef fect of chlorination is equivalent to 6.25 percent mortality. When this value was combined with the nonthermal mortality of 18.5 percent estimated above, the result was a total nonthermal mortality of 23.59 percent based on Equation 6.1-2. The entrainment simulation data (two tests) were inadequate for analysis of the thermal effects on spot. Therefore, the thermal mortality of spot was estimated from the thermal shock data of the present study (Meldrim 1978). These studies indicated that early j uvenile spot acclimated to near 17*C experienced no mortality upon a temperature increase of ll*C and complete mortality at a 15'c increase. Specimens acclimated to near 25*C experienced 50 and 100 percent mortality at delta-Ts of 8 and 11*C, g respectively. Applying a weighted, iterative regression to these values, W the following probit regression model was obtained for the thermal mortality: M = -37.16428 + 1.78425 TE - 0.66867 TA (Equation 6.1-3) where M = probit of 96-hour thermal mortality TE " exposure temperature (*C) T = acclimation temperature (*C) A Thermal mortality for spot can be derived from the above equation using weekly temperatures computed from the maximum daily mean water temper-ature at Reedy Island during 1970-1982 and the temperature rise at Salem Units No. I and 2. Total entrainment mortality ( ) is then computed from the thermal (M ) and nonthermal (M " ) morta ities based on Equation 6.1-1. Table 6.1-14 summarizes the estimated weekly nonthermal, thermal, and total entrainment mortality for spot at Salem Units No. I and 2. Blueback Herring, Alewife, and American Shad Since all three of these species belong to the clupeid family, their entrainment survivals are evaluated collectively. One j uvenile blueback herring , but no American shad , was taken in onsite survival samples. 6.1-14
Salem 316(b) Demonstration l Fourteen and eight alewife /Alosa spp. juveniles were taken at the dis- , charge and intake , respectively. Only a single individual from each group survived the 24-hour observ scion period, indicating intake and discharge mortalities of 87.5 and 92.9 percent, respectively. This yielded a Salem-induced mortality of 42.9 percent. However, considering _ the small sample size, little confidence can be placed in this estimate. I Af ter reviewing much of the. published nonthermal entrainment work,
.Jinks et al. (1980) concluded that entrainment mortality for c.lupeids at
. brackish / marine sites ' ranged from 21 to 60 percent. These values are therefore used in this study as low and high estimates of nonthermal mortality 'for clupeids. When combined with mortality from chlorination of 6.25 percent, the low and- high estimates of total nonthermal mortality are 25.94 and 62.50 percent, respectively.
Thermal mortality was evaluated using the entrainment simulation data. Af ter adjusting for 18.3 percent control mortality, the following probit regression model was developed for postlarval blueback herring: Mt = 1.112 - 0.096 TA- 0.029 log 10 t + 0.171 TE- (Equation 6.l W
~
(R = 0.358) wher'e t stands for exposure time in minutes and otaer symbols are the same as in Equation 6.1-1. A similar probit regression equation was developed by Oak Ridge National
~ Laboratories' (ORNL) (Vaughan 1982) for alewife yolk-sac larvae :
M '= - 14.194'- 0.015 T A+ 2.158 log 10 t + 0 A73 T E quadon 6.1-0 (R = 0.51)
- Because the values from the present study seem less reasonable, the ORNL thermal-effect model is adopted for subsequent analysis. The choice is not highly critical because it is expected that most of the entrainment mortality is caused by nonthermal effects. The weekly thermal mortality
, values are computed using the ORNL model with the weekly temperature at Reedy Island and the temperature rises through Salem Units No.1 and. 2 as input. The low and high estimates of total entrainment mortality rates for the clupeids are computed by combining the thermal mortality with the low and high values for'nonthermal mortality; they are pre-sented in Tables 6.1-15 and 6.1-16, respectively. Although the entrain-ment survival rates estimated above may be applicable to American shad, none were entrained at Salem in 1977-1981 nor are they expected to be entrained in the future. i 6.1-15 _. . __ ._-_ . _ . . _ _ . . _ . . . _ . _ - _ _ _ ~ , _ - _ _ . , - _ _
Salem 316(b) Demonstration Atlantic Croaker h Only nine croaker juveniles and one larva were collected during onsite entrainment survival studies in 1977-1982. Because of the small sample size, calculation of nonthermal effects was not considered justifiable. Based on the survival of 404 croaker larvae collected at the intake and 377 at the discharge at the Brunswick Steam Electric Station on Cape Fear, Norh Carolina (Copeland et al.1975), a nonthermal mortality of 36 percent was astimated. When combined with the chlorine mortality of 6.25 percent, the total nonthermal mortality was estimated at 40 percent. Thermal mortality of entrained croaker was estimated from the limited entrainment simulation data on early juveniles. The following probit regression model was developed to combine the effects of acclimation and exposure temperatures: M = -1.990 + 0.238 TE - 0.038 T A S"# " *
~
(R = 0.331) This model predicts an LT50 of 32*C for croaker acclimated to 17'C. How-ever, values above and below LT50 seemed to be biologically unrealistic. To remedy this situation, results from Copeland et al . (1974) were used by assuming that the critical thermal maxima (CTM) are equivalent to 99.99 percent mortality. Copeland et al. (1974) presented a multiple-regression model that pre-dicted CTM values of 34.6, 37.3, 39.1, and 41.5*C for juvenile croaker acclimated to 18, 23, 28, and 33*C, respectively. When combined with the LT50 estimated from the simulation data, the following equation was , obtained: Mt = -35.451 + 1.663 TE - 0.751 T g (Equation 6.1-7) The weekly nonthermal, thermal, and total entrainment mortality values for Atlantic croaker are summarized in Table 6.1-17. Striped Bass No striped bass eggs or larvae were collected during entrainment survival studies at Salem. Accordingly, entrainment survival rates were estimated based on the extensive studies conducted with striped bass at the Hudson River power plants . Vaughan (1982) reported a mortality rate of 66 percent for striped bass eggs, calculated from data obtained at the intake and discharge at Indian Point from 1973 to 1978. He also esti- ~ mated initial nonthermal and 24-hour latent entrainment mortalities of striped bass yolk-sac and post yolk-sac larvae as 44 and 13 percent , respectively, based on larval table studies at the Bowline, Rosecon, Indian Point, and Danskammer generating plants. A chlorination mortality 6.1-16
Salem 316(b) Demonstration
/G V of 6.25 percent was factored into the nonthermal. effect by assuming 100 percent mortality of entrained striped bass eggs and larvae during periods of chlorination. Thermal mortality of striped bass larvae was estimated by Vaughan (1982) using the following probit regression model:
M = -7.771 - 0.096 T + . 00 log 10 t + 0.346 T E (Equation 6.1-8) t A (R = 0.44) Vaughan's thermal effect model predicts 5, -50, and 95 petcent mortality
'at 31.8,'36.6, and 41.3*C, respectively, at an acclimation temperature of' 17.5*C and an exposure duration of 6 minutes. It is unlikely that 4
thermal effects will contribute to entrainment mortality of striped bass eggs since the River temperature plus the delta temperature for Units No. I and 2 is not expected to exceed the foregoing 5, 50, and 95 percent
. thermal mortality limits during the time of their occurrence.
The estimated weekly nonthermal, thernal, and total entrainment mortal-ities for striped bass eggs and' larvae are presented in Tables 6.1-18 and 6.1-19, respectively. , i White Perch Since no white perch prolarvae were taken during onsite entrainment survival studies, estimates of nonthermal-induced mortality for this life stage were derived from the literature. Vaughan (1982) calculated, from pooled larval-table ' data collected at discharge temperatures <30*C, an initial nonthermal mortality of 0.44 for striped bass prolarvae at the Hudson River plants. This value was used by Boreman and Goodyear (1980) for the Hudson River white perch population and was also used in this study for the white perch prolarvae in the Delaware estuary. Since the i latent nonthermal mortality was unavailable, the combined (thermal and nonthermal)' 24-hour latent mortality of 0.13 reported by Vaughan (1982) was also used. This resulted in a total nonthermal mortality of 0.51 for the white perch prolarvae. - An attempt to calculate thermal entrainment mortality of white perch . prolarvae from present-study simulated entrainment data was unsuccessful ! because the range in test conditions was insuf ficient to- develop a realistic model. Based on laboratory studies conducted by EA (1978), j- Vaughan (1982) developed the following probit regression of white perch prolarvae: M = -15.814 - 0.112 T + 2.796 log t + 0.545 T (Equation 6.1 4 g A 10 E (R = 0.37) 7 This model suggests that thermal effects will contribute minimally to (V the total entrainment mortality of white perch prolarvae at Salem. The estimated weekly nonthermal, thermal, and total entrainment mortalities for white perch prolarvae are' presented in Table 6.1-20. 6.1-17
Salem 316(b) Demonstration For white perch postlarvae, estimates of nonthermal mortality were derived from the literature since no postlarvae were taken during onsite entrainment survival studies. From pooled larval-table data, Vaughan (1982) calculated initial nonthermal mortalities for white perch post-larvae of 0.0 (n = 356 specimens), 0.38 (n = 605), 0.78 (n = 63), and 0.0 (n = 87) at Bowline Point , Roseton, Indian Point, and Danskammer Point generating plants, respectively. Based on these four values, avecage mortality, weighted by sample size, was 0.25. Vaughan also reported a combined (nonthermal and thermal) 24-hour latent mortality of 0.0 for white perch postlarvae. Assuming no latent mortality, the total nonthermal entrainment mortality is therefore estimated to be 0.25. The thermal entrainment mortality of white perch postlarvae was calcu-lated from present-study simulated entrainment data. The following probit regression model was developed to combine the effects of acclima-tion temperature (T ), exposure temperature (TE , and exposure duration (t) inestimatingthe96-hourthermalmortality: M = -7.594 - 0.063 T + 4.057 log t + 0.308 T adon 6.W A 10 E (R = 0.48) The model above suggests that thermal effects will not contribute sub-stantially to entrainment mortality of white perch postlarvae at Salem. The estimated weekly nonthermal, thermal, and total entrainment mortal-ities for white perch postlarvae are presented in Table 6.1-21. h Bay Anchovy As evidenced by the high sampling-induced mortality occurring in present-study entrainment control samples, bay anchovy are very sensitive to mechanical / physical stress, and mechanical damage is a large factor in bay anchovy entrainment mortality. Estimates of nonthermal entrainment mortality for bay anchovy eggs could not be obtained from present-study onsite data because the small trans-parent eggs could not be detected in the survival samples. Literature data on the nonthermal component of entrainment mortality were also unavailable; therefore, the nonthermal mortality of eggs was assumed to be 100 percent. As noted below, bay anchovy egg viability in the vicin-ity of Salem station is typically only about 20 to 30 percent. This factor was not accounted for in estimating entrainment losses, and represents a conservative bias in this analysis. Nonthermal mortality of bay anchovy larvae was estimated from present study onsite data at temperatures below 30*C, the temperature below which thermal response is not likely to be induced. The estimate of the nonthermal component of mortality for larvae based on data from discharge samples observed through 24 hours is 100 percent, whereas control mor-tality is estimated to be 99.5 percent. For further analysis, the nonthermal mortality of larvae is assumed to be 100 percent. 6.1-18
Salem 316(b) Demonstration Using the 30*C thermal response criterion, the nonthermal mortality l component for bay anchovy juveniles and adults was similarly estimated l from onsite data. The estimate for juveniles based on data from discharge samples observed through 24 hours is 96.9 percent; control mortality was estimated at 91.8 percent. Based on data from discharge samplas observed through 24 hours, the estimate for adults is 94.3 percent; control mortality was estimated to be 76.5 percent. The nonthermal mortalities for juveniles and adults were combined for use in subsequent analyses and a combined estimate of 97 percent was obtained. To estimate the thermal-related mortality entrainment response data for bay anchovy, larvae at temperatures >30*C and with control mortality <20 percent were analyzed. The following probit regression model was developed: M g = -27.510 + 1.089 T E
-0.m T +g 2.527 log 10 t (Equadon 6.1-W (R = 0.351)
Estimates of mean tolerance limit (LT50) based on this model are compa-rable to those reported for bay anchovy in the literature. At 24*C ambient temperature and 60-minute exposure duration, the model predicts , an LT50 of 35.5'C for bay anchovy larvae compared to 33.4*C reported by EA (1978). At an exposure duration of 180 minutes and acclimation o temperature of 26*C, the model predicts an LT50 of 31.1*C compared to V 32*C reported by Chung and Strawn (1982). However, estimates of the thermal response of bay anchovy at temperatures above and below LT50 appear to be unrealistic. The magnitude of the exposure temperature coef ficient (1.069) indicates an unrealistically steep thermal response gradient. The difference in exposure temperature between 10 and 90 percent mortality estimates was only 2.4*C. In comparison, thermal mortality data for other specie,s (white perch, alewife, and weakfish) indicate a range of 6*C (Boreman et al. 1982; Greges and Schubel 1979). A revised thermal mortality probit model was developed for bay anchovy based on the average difference in exposure temperature for the above species at the 10 and 90 percent mortalities and the 50 percent mortality calculated from the present-study model described in Equation 6.1-11. The resultant probit thermal mortality model was : Mg = - 7.751 + 0.427 T - 0. m T + 0.995 log t (Equation 6.1-12) E A 10 This model appears reasonable for bay anchovy and is used in all subse-quent analyses of bay anchovy thermal mortality. Although this model was developed from larval data, it was used to predict thermal-related mortality for the juvenile and adult life stages as well. This was considered a conservative approach since larvae are generally more sensitive than the later life stages. m ( ) The estimated weekly nonthermal, thermal, and total entrainment mortali-ties for bay anchovy juveniles and adults are presented in Table 6.1-22. 6.1-19
Salem 316(b) Demonstration As shown, total mortality for bay anchovy juveniles and adults varied between 97.2 and 98.0 percent. As discussed previously, total mortality h for bay anchovy eggs and larvae, all attributable to nonthermal effects, was estimated at 100 percent. Weakfish Estimates of nonthermal mortality of weakfish eggs were unavailable either from present-study data or from the literature. Therefore, a nonthermal mortality of 100 percent was conservatively assumed for this life stage. As noted below, weakfish egg viability ir. the vicinity of Salem station is typically only about 60-70 percent. This factor was not accounted for in estimating entrainment losses, and represents a conser-vative bias in this analysis. The nonthermal mortality of weakfish larvae at Salem was estimated from the onsite survival data and from the literature. The onsite survival data considered discharge specimens collected at discharge temperature 130*C whereas specimens collected at the intake, except those taken ' during chlorination, were pooled to increase the sample size. The 48-hour survival of 23 discharge specimens was 0.3043, whereas the 48-hour survival of 37 intake specimens was 0.3514. Applying Abbott's formula (Equation 6.1-1) yields an adjusted nonthermal mortality of 0.1340. However, the high control mortality in this study indicates weakfish are susceptible to substantial collection and holding stress. An alternative estimate of the nonthermal entrainment mortality was O calculated based on the survival data for weakfish larvae at the Bruns-wick Steam Electric Plant on the Cape Fear estuary, Necth Carolina ( Copeland et al . 1975 ) . Based on Copeland's data, initial survival of 101 intake specimens was 0.5644 whereas survival of 77 discharge speci-mens, under conditions of no heat rejection, was 0.3247. Applying Abbott's formula yields an adjusted mortality of 0.4247. Even though the time elr.psed was not reported for these data, since most mortality occurs within 3 hours after collection in the present study, the mortality estimate from Copeland's data may be representative of latent mortality. Based on the discussion above, a nonthermal entrainment mortality of 0.4 was conservatively estimated for the weakfish pro- and post-larvae in subsequent analysis. For weakfish juveniles , the nonthermal mortality at Salem was estimated from onsite entrainment survival data collected at discharge temperatures f30*C. The 96-hour survival of 24 intake specimens was 0.2273, whereas survival of 63 discharge specimens was 0.1111, yielding an adjusted mortality of 0.5112. ;or simplicity, a value of 0.5 was used as the nonthermal mortality for weakfish juveniles in subsequent analys is . Initially, an attempt was made to obtain specific thermal entrainmeut mortality models for each of the weakfish life stages: prolarvae, postlarvae, and juveniles. However, the development of realistic stage-specific thermal models from present-study simulated entrainment data proved unsuccessful because of the insufficient range in test conditions 6.1-20
~ . - . - --
Salem 316(b) Demonstration
) for each life stage. Therefore, the present-study simulated' data for the three life stages were combined to develop an empirically based model.
A weighted, iterative regression procedure resulted in the following probit model: Mg = -2.551 + 0.263 T E- 0.088 Tg + 0.197 log 10 t (Equation 6.1-13) (R = 0.584)
- Although estimates of LT50 from this model appear reasonable, thermal response above and below LT50 appears unrealistic. The magnitude of the exposure-temperature coefficient (0.263) and the intercept coefficient
(-2.551) indicate an unrealistically shallow thermal response gradient; the difference in exposure temperature between LT10 and LT90 is about 10*C. Other thermal mortality models developed from studies.on white
. perch and alewife (Boreman et al.1982) and weakfish (Greges and Schubel 1979) indicate a range of about 6*C between LT10 and LT90. Consequently, a revised model was developed using the LT50 values calculated from the model described in Equation 6.1-13 and the range of 6*C for LT10 and UI90 values. The following probit thermal mortality model was developed:
1 Mt = - 9.0158 + 0.4272 TE- 0.0923 Tg + 1.2856 log 10 ' (Equation 6.1-14)
. <g
- This model appears reasonable and is used in subsequent analysis. The estimated weekly nonthermal, chermal, and total entrainment mortalities are presented in Table 6.1-23 for weakfish prolarvae and postlarvae and in Table 6.1-24 for weakfish juveniles.
Neomysis americana < Onsite survival data collected at Salem during the present study indicate a minimal ef fect of the nonthermal component of entrainment mortality. At discharge temperatures below 29*C and af ter adjusting for control mortality, the intake and discharge survivals were 92.7 (n = 2,914) 'and 82.1 percent (n = 2,213), respectively. This yielded a plant-induced
~
mortality.of 11.5 percent . This result is consistent with other entrain-
- ment survival studies on N. Americana. Cannon et al. (1977) reported that initial survival in intake and discharge samples was 90 percent (n =
j 101) and 85 percent (n = 178), respectively, at discharge temperatures
<29'C at Bowline Point on the Hudson River during 1976. Latent survival was not significantly reduced in discharge samples in this study. Lauer et al. (1974) reported no detectable entrainment-related mortality of Neomysis at Indian Point on the Hudson River when discharge _ temperatures were '<31.1*C, except during periods of chlorination.
Simulated entrainment data generated in the present study were used to , estimate thermal-related entrainment mortality. The following probit ! ' (). regression model was developed to correlate the effects of observed delta-T,' acclimation temperature, and exposure duration: l-6.1-21 1
Salem 316(b) Demonstration M = -9.444 + 0.486 T - 0.133 T + 1.330 log g E 4 10 t (Equation 6.1-15) g (R = 0.531) The estimated weekly nonthermal, thermal, and total entrainment mortal-ities for N_. Americana are presented in Table 6.1-25. Gammarus tigrinus Group Onsite , rival data during the present study at discharge temperatures below 3P u indicate insignificant nonthermal effects on Gammarus spp. as a result of entrainment. After eliminating tests with > 20 percent conditional mortality, intake and discharge survival was 92.7 percent (n = 1,888) and 91.5 percent (n = 1,513), respectively. This yields a plant-induced mortality of 1.4 percent. The literature also suggests few or no nonthermal effects on Gammarus spp. except during periods of chlorination. Lauer et al. (1974). reported < 10 percent (based on 307 samples) mortality of Gammarus at Indian Point at temperatures below 32*C, except during chlorination when discharge mortality ranged from 18.8 to 45.5 percent. Cannon et al. (1977) reported that initial survival of G. daiberi at four Hudson River facil-ities (Rosecon, Danskammer, Bowline Point, and Lovett) was generally similar at intake and discharge at temperatures below 33*C with the discharge survival ranging from 87 to 98 percent. Ginn et al. (1977) reported consistently high survival of G. tigrinus in 5-minute simulated entrainment tests at temperatures below 34.2*C without chlorination. They further reported that the lethal effect of chlorine was considerably increased at higher delta-Ts. At an ambient temperature of 12.2*C, a total residual chlorine (TRC) concentration of 0.44 mg/ liter resulted in a mortality rate 58 percent higher than the rate without chlorination. At delta-Ts of 16.7 and 22*C above the same ambient temperature, the mean 24-hour survival under the same chlorine concentration was only 9.1 percent , whereas the survival without chlorination was 87.5 percent. The effect of chlorination is factored into the computation by assuming 58 percent mortality during periods of chlorination, which are scheduled to occur 6.25 percent of the time. As a result, chlorine mortality was estimated at 3.625 percent. When this value was combined with the nonthermal mortality of 1.4 percent estimated previously, a total non-thermal mortality of 4.95 percent resulted. The thermal components of entrainment mortality were evaluated using the simulated entrainment data at temperatures > 32*C, but excluding samples with control mortality >_ 20 percent. A probit regression model was developed to correlate the ef fects of observed delta-T, acclimation temperature, and exposure duration: Mt = -8.068 + 0.436 TE + 0.250 TA- 13. 71 log 10 t (Equation 6.1-M) (R = 0.774) 6.1-22
Salem 316(b) Demonstration Although this equation provides a reasonable fit to the simulated en-trainment data, the negative coefficient of the exposure duration pre-dicts that as the exposure duration increases, mortality decreases. ' This aberration is probably caused by the small number (two) and proximity of l the exposure times examined and suggests that the model is biologically l unreasonable and/or inaccurate outside the range of the data. Therefore, j data reported in the literature were used to derive a more reasonable l mod el . Ginn et al. (1974) presented figures that included a wide range , of data for ambient temperature (2.5-25.0*C), exposure temperature (25.0- ' 38.5'C), and exposure duration (5, 30, 60 minutes, and 48 hours) . These values were used in developing the following probit regression model: (Equation 6.1-17) M = -11.942 + 0 585 TE - 0.269 T g+ 1.205 log 10 t (R = 0.515) The estimated weekly nonthermal, thermal, and total entrainment mortal-ities for Gammarus spp. are presented in Table 6.1-26. 6.1.4 ESTIMATING THE RATE OF ENTRAINMENT LOSSES Estimates of projected entrainment densities, percent survival of entrained organisms, and expected plant withdrawal volumes are required to predict entrainment losses for each target species at Salem under ('N future operation. Estimates of entrainment densities and entrainment V survival rates for each target species are presented in Sections 6.1.2 and 6.1.3, respec tively. Future plant withdrawals can be approximated frcm the refueling outage schedule described in Section 3.4. Refueling outages for each unit are scheduled to occur at approximately 18-month intervals and last for approximately 10 weeks during spring or late fall. One unit at a time is scheduled to be out of service in two out of three years. A spring and fall outage will occur approximately every third year. It is assumed that during refueling all four SWS pumps and one CWS pump of the unit out of service will remain in operation. The number of CWS pumps expected to be in operation each week under each of these scenarios is presented in Table 6.1-27. For purposes of comparison, a no-outage scenario is presented in the same table. When not down for refueling , both units are assumed to operate at 100 percent power and pumping capacity. Operating scenarios also include a stepwise one-seventh reduction or acceleration per day in both power and pumping capacity during the week inanediately preceding and following a refueling outage. The number of CWS pumps in operation, as summaris:ed in Table 6.1-26, is used in the projection of entrainment losses for the secondary target species. However, the assumption of 100 percent power output and pumping capacity used in Table 6.1-26 has proved unrealistic. Based on the operational 7 data from Salem during 1980-1982, under " typical" full operation, Unit (d No. I can be expected to operate at 96 percent power and 88 percent pumping capacity, and Unit No. 2 at 95 percent power and 83 percent pumping capacity. The number of CWS pumps operating each week under the 6.1-23
Salem 316(b) Demonstration " typical" full operation for the various outage scenarios is presented in Table 6.1-28. These pump operations are used in subsequent projections lll of entrainment losses for the three primary target species (white perch, bay anchovy, and weakfish) . Projected entrainment losses for eacn species are computed on a daily basis using the following equations: Daily Entrainment loss = CWSl. +1 SWSl. +1 CWS2. L+ SWS2.1 (Equation 6.1-18) CWSl . = K1 x Density. x (F. - R x F.1 )/(1 - R + R x F.1 ) (Equation 6.1-19) 1 1 1 SWSl. = K2 x Density. x (1 - R) (Equation 6.1-20) 1 1 where CWSl g
= entrainment loss at Unit No. 1 CWS on the ich day SWSI. = entrainment loss at Unit No. 1 SWS on the ich day 1
CWS2. = entrainment loss at Unit No. 2 CWS on the ich day 1 SWS2. = entrainment loss at Unit No. 2 SWS on the ith day 1 K1 = plant withdrawal at Unit No. 1 CWS on the ith day
= 11.672 m /sec x 86400 seconds x the number of CWS pumps operating in Unit No. 1 lll '
K2 = plant withdrawal at Unit No. 1 SWS on the ich day
= 0.686 m /sec x 86400 seconds x the number of SWS pumps operating in Unit No. 1 Density g = estimated entrainment density on the ith day F. = estimated total entrainment mortality at 1
Unit No. 1 CWS on the ith day R = recirculation factor Computation of CWS2. and SWS2. entrainment losses at the cooling and service water cyste$s of Saled Unit No. 2 is based on equations similar to Equations 6.1-19 and 6.1-20. One hundred percent mortality was assumed for organisms entrained by the SWS. A detailed description of the computation procedure used for estimating the rate of entrainment losses is provided in Section 2 of Appendix I. The daily entrainment losses are summarized on a weekly basis for each target species entrained at Salem under the following operating scenarios: no outage, spring outage, fall outage, and combined spring and fall outage. Tables 6.1-29 through 6.1-50 summarize projected entrainment losses for each species under the assumptions of no outage and no recircu-lation. Tables 6.1-50 and 6.1-51 summarize estimated entrainment losses under all plant operating scenarios for fish taxa and for target macro-invertebrate taxa, respectively. (The effect of outages on estimated annual entrainment reflects the period of involvement of each species with Salem.) 6.1-24
l Salem 316(b) Demonstration l ID Depending on plant operating conditiong, estimated anngal entrainment losses for spot range from 37.047 x 10 to 43.031 x 10 early juve-niles (Table 6.1-51). Since these losses occur from mid-May through early July, with peak involvement during the latter part of May, annual entrainment is affected by the spring' outage condition. Estimated annua6 1 entrainment losses of gtlantic croaker are projected to be 0.791 x 10 larvae and 5.158 6 x 10 juvenilesforfagloutage and combined outage and 1.115 x 10 larvae and 7.695 x 10 juveniles for no outage and spring outage. As discussed in Section 6.1.2.2, these projected entrainment densities were derived from both onsite entrainment and river abundance data. Annual entrainment is reduced under the fall outage scenario. Among the three clupeid target species, American shad was not found in Salem entrainment collections (Table 6.1-12). This is consistent with the known biology of American shad in the Delaware River ( Appendix III), where spawning occurs a considerable distance upriver of Artificial Island. Consequently, entrainment projections are not made for this species. Entrainment data for blueback herring and alewife were limited. The lack of entrainment survival specimens prompted an estimation of a high and low entrainment mortality range for the two species (Section 6.1.3). Based on the low mortality estimates, annual entrainment Igsses for blueback herring early juveniles are projegted to be 0.231 x 10
.O under no outage and fall outage and 0.171 x 10 under spring outage and combined outage. Based on high entrainment mortality estimates and the same plant operating scenarios, estimated annual entrainment Igsses of blueback hegring early juveniles are projected to be 0.512 x 10 and 0.368 x 10 , respectively. For alewife, using low entrainment mogtality estimateg, the projected annual entrainment losses are 0.087 x 10 and 0.056 x 10 early6 juven es under 6these plant operating conditions, or 0.193 x 10 and 0.119 x 10 early juveniles if high mortality estimates are used.
Some entrainment losses were also projected for Alosa spp. Based on the low entrainment mortality rates for blueback herring and alewife, the annual entrainmegt losses of Alosa spp. early juveniles were estjmated to be 3.173 x 10 under no outage and fall outage and 2.075 x 10 . under spring outage and combined outage. Based on the high entrainment mogtality, the anngal entrainment losses are estimated to be 7.055 x 10 and 4.410 x 10 , respectively. Early life stages of striped bass were rarely found in Salem entrain-ment collections, apparently because of the infrequent entrainment sampling from 1977 to 1982 during their period of peak abundance. Therefore, river abundance data near Artificial Island were used to estimate the likely densities of entrained striped bass. Under operating conditions of no outage 6and fall outage, the Projected 6 annual entrainment losses are 1.720 x 10 eggs and 0.801 x 10 larvae,
.[3'~ ') respectively. Under conditions of gpring outage and comgined outage, the projected losses are 1.043 x 10 eggs and 0.524 x 10 larvae, respectively.
6.1-25
Salem 316(b) Demonstration Estimatedannuafentrainment lgsses of whi':e perch are projectgd to range from 0.655 x 10 to 0.942 x 10 prolarvae, and from 1.038 x 10 to 1.540 x 106 postlarvae under various plant operating conditions. These projections are based on entrainment densities estimated based on both the onsite entrainment data and the 0.5-m plankton net data collected in the Delaware River near Artificial Island. No entrainment losses were projected for white perch eggs because of their very low density in both data sets and, consequently, their unlikely involvement with Salem. For bay anchovy, entrainment losses are projected separately for eggs, larvae,andjuveniles/adugts. The projgeted annual entrainment losses of eggs range from 9.09 x 10 to 9.11 x 10 , depending on plant operat-ing conditions. These estimates of entrainment losses are probably biased high- perhaps by 70-80 percent--since bay anchovy egg viability, based on samples collected near Salem during 1974 through 1978, ranges from only 6.8 to 58.9 percent. Theestimagedannualegtrainment losses of bay anchovy larvae range from 2.04 x 10 to 29 05 10 , while9the losses of juveniles / adults range from 0.33 x 10 to 0.35 x 10 , depending on plant opezating conditions. Entrainment losses of weakfish are projected separately for eggs, pro-larvae, postlarvae, and juveniles. The estigated annual egtrainment losses of weakfish eggs range from 5.49 x 10 to 5.52 x 10 , depending on plant outage schedules. These estimated losses may be biased high, perhaps by 30 to 40 percent, since weakfish egg viability near Salem has averaged about 60 to 70 percent. Annualentrainmenglossesofweakgish g prolarvae are proje::ted to range between 12.81 x 10 and 12.95 x 10 6 Annual losses gf postlarvae are projected to range between 17.21 x 10 and 17.54 x 10 , whereas the numbers of weakfish jugeniles lost to gn-trainment are projected to range between 25.08 x 10 and 25.15 x 10 annually. For N_. americana and Gammarus spp., entrainment densities are estimated by applying seasonally weighted ratios of entrainment versus river density to the river abundance data (Section 6.1.2.2). Estimates of annual entrainment losses f o r N,,, americana under no outgge, spring 9 outage,fagloutage,angcombinedoutageare222.1x10,220.7x10, 215.0 x 10 , 214.4 x 10 , respectively. Estimates of annual entraingent losses fgr Gammarus g spp, under the same plant scenarios are 6.9 x 10 , 6.0 x 10 , 6.8 x 10 , and 6.0 x 10 9, respectively. The above estimates represent projected entrainment losses af the early life stages of each target fish species and all life stages of the two target macroinvertebrate taxa under four plant operating scenarios. For each species, the range of losses is related to the seasonal involvement mich Salem. Section 6.3 assesses the biological significance of these luses by putting them into perspective with the source populations from wh.' h the organisms are removed. The equivalent adult, conditional mort 11ity rate, production foregone, or lost reproductive potential approach is used, either alone or in combination, depending on the biology of the species involved. g 6.1-26
n Salem 316(b) Demonstration ('v) TABLE 6.1-1 RANK AND PERCENT TOTAL CATCH OF MACR 0 INVERTEBRATE PLANKTON , 1978 Taxon Rank Percent
**Neomysis americana 1 81.6 Rhithropanopeus harrisil 2 11.2
**cammarus spp. 3 2.2 Edotes triloba 4 1.7 Corophium spp. 5 0.7 Brachyura 6 0.7 Leucon americanus 7 0.4 Palaemonetes @ 8 0.4 Crangon septenspinosa 9 0.3 Hydrozoa (Medusae) 10 0.2 Blackfordia virginica 11 0.2 Eca minax 12 0.1 Monoculodes edwardst 13 0.1 Mudibranchia 14
- Aegathoa medialis 13
- Cyathura polita 16
- Melita nitida -
17
- Parapteustes spp. 18
- Argulus app. 19
- Chiridotes atevra 20
- Labidocera aestiva 21
- Polychaeta """ 22
- Hydrozoa No. 1 (Medusae) 23
- Callinectes sapidus 24
- Hirudinea 25 *
-Nemopsis bachel 26
- Caanidinidea Lunifrons 27
- g ~s Monoculodes spp. 28 *
( i Phistidium spp. 29 *
\~- Leotocheirus plumulosus 30
- oligochaeta 31
- Chiridotea spp. 32
- i Bopyridae 33
- Turbe11 aria 34
- Macoma spp. 35
- Rhynchocos ta 36
- Orchestia spp. 37
- Actiniaria 38
- Leuconidae 39 *
- Lieutus polyphemus 40
- j Chironomidae 41
- Platyhelminthes 42
- Castropoda 43 *
, Haustorildae 44 * ! Sougainvillia spp. 45
- j Cirripedia - *
! Parametopella cypris -
- I Stylochus ettioticus - *
! Amphipoda -
- Annelida -
- Leptochelia savignvi -
- Diptera -
- l Diadumene leucolena -
- l Cirolana -
- Nematoda -
- Capre111dae -
- Hydrozoa -
- Insecta -
- l l
I * = Indicates less than 0.1 percent. l /'} ** = Indicates target species. l s_ ,e - = Not ranked. i , L
Salem 316(b) Demonstration O'~h TABLE 6.1-2 ESTIMATED ENTRAINMENT DENSITIES OF Neomysis americana AND Gammarus spp. AT THE SALEM GENERATING STATION FROM ENTRAINMENT ABUNDANCE PROGRAM, 1977-1980 , En{rg.nment Densities (No./m ) Date Neomysis americana Gammarus spp. 1977 AUG 31- 147.342 5.331 SEP 1 DEC 7-8 0.277 0.830
~
1978 FEB 27 0.131 2.566 MAR 2-3 0.181 1.072 MAR 16 0.590 0.950 APR 19-20 66.203 5.152 JUN 28-29 430.755 16.153 JUL 12-13 185.678 15.732 JUL 27-28 16.578 3.216 AUG 10-11 60.573 6.041 AUG 31- 109.522 7.376 SEP 1 {q j SEP 13-14 776.950 24.022 10.708 OCT 11 2.881 NOV 1 17.057 2.246 NOV 21-22 104.950 0.491 DEC 13 84.757 3.240 - 1979 MAR 27-28 0.345 12.995 JUN 6-7 40.463 28.667 l JUL 5-6 535.301 18.171 i JUL 12-13 196.947 16.236 ! JUL 19-20 194.003 26.727 JUL 25-26 442.287 31.143 AUG 22-23 58.890 2.950 OCT 17-18 668.094 3.456 OCT 31- 35.211 5.646 NOV 1 { 1980 l JAN 23-24 1.277 5.007 MAR 19-20 29.563 3.494 APR 16-17 0.169 51.661 APR 30- 6.181 13.853 , ( MY 1 MAY 21-22 331.452 19.511 L'O J
1 Salem 316(b) Demonstration TABLE 6.1-2 (page 2 of 2) Entrainment Densities (No./m ) Date Neomysis americana Gammarus spp. 1980 (Cont.) JUN 2-3 129.692 7.203 JUN 6-7 565.990 6.027 JUN 10-11 400.807 8.396 JUN 14-15 158.960 7.265 JUN 18-19 764.760 3.746 JUN 22-23 798.000 4.170 JUN 26-27 299.-873 5.046 JUN 30- 151.010 4.940 JUL 1 JUL 4-5 199.975 7.205 JUL 8-9 62.430 6.675 JUL 12-13 147.505 9.495 JUL 16-17 63.125 9.015 JUL 20-21 226.214 4.094 JUL 24-25 144.880 7.880 4 h JUL 28-29 AUG l-2 49.495 95.771 5.380 7.641 AUG 5-6 42.235 6.520 AUG 9-10 44.430 3.815 AUG 13 49.380 3.460 AUG 17-18 373.800 4.375 AUG 21-22 174.577 1.079 AUG 25 10.660 1.264 AUG 29-30 72.550 0.825 SEP 2-3 95.650 0.310 SEP 6 82.627 0.246 SEP 10-11 64.985 0.165 SEP 14-15 233.820 0.070 SEP 18 80.120 0.010 , SEP 22 63.627 0.013 SEP 26-27 10.600 0.080 OCT 1 9.380 0.090
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Salem 316 (b) Demonstration O 3 (_/ TABLE 6.1-4 ESTIMATED EGG ENTRAINMENT DENSITIES (No./m ) 0F FISH SPECIES AT THE SALEM GENERATING STATION FROM ENTRAINMENT ABUNDANCE PROGRAM (1977-1982) Total Total Taraet Species Densities Montarget Eg8 Bay White Atlant&C Blueback Ame ric an Strtped Spectes Cate Densities Anchove Weakfish Perth g Croaker Alewife Herring Shad _ Sass Densities 1977 AUG 31- 0.226 0.204 0 0 0 0 0 0 o u 0.022 SEP 1 DEC 1*8 0 0 0 0 0 0 0 0 0 0 0 1978 FEB 27 0 0 0 0 0 0 0 0 0 0 0 MAR 2-3 0 0 0 0 0 0 0 0 0 0 0 MAA L6 0 0 0 0 0 0 0 0 0 0 0 apt 19-20 0.063 0 0 0 0 0 0 0 0 0.006 0.057 JUN 28-29 1.162 1.162 0 0 0 0 0 0 0 0 0 JUL 12-13 24.936 24.924 0.002 0 0 0 0 0 0 0 0.010 JCL 27-28 0.157 0.153 0 0 0 0 0 0 0 0 0.003 AUG 10-11 3.037 3.037 0 0 0 0 0 0 0 0 0 A"G 31- 0 0 0 0 0 0 0 0 0 0 0
$17 1 SEP 13-16 0 0 0 0 0 0 0 0 0 0 0 OCT ll 0 0 0 0 0 0 0 0 0 0 0 MV 1 0 0 0 0 0 0 0 0 0 0 0 NOV 21-22 0 0 0 0 0 0 0 0 0 0 0 DEC 13 0 0 0 0 0 0 0 0 0 0 0 1979 JUN 6 8.952 1.221 0 0 0 0 0 0 0 0 0.738 JUL 5-6 149.252 149.229 0.012 0 0 0 0 0 0 0 0.012 JUL 12-13 13.418 12.825 0.017 0 0 0 0 0 0 0 0.577 JUL 19-20 2.726 2.678 0.002 0 0 0 0 0 0 0 0.066 JUL 25-26 5.277 5.060 0 0 0 0 0 0 0 0 0.16e }. AUC 22-23 0.577 0.567 0 0 0 0 0 0 0 0 0.010 g 1 OCT 17-18 0.002 0.002 0 0 0 0 0 0 0 0 0 V OCT 31- 0.010 0.010 0 0 0 0 0 0 0 0 0 Nov 1 1980 JAN 23-24 0 0 0 0 0 0 0 0 0 0 0 MA1 19-20 0 0 0 0 0 0 0 0 0 0 0 APR 16-17 0.009 0 0 0.003 0 0 0 0 0 0 0.006 APR 30- 0.002 0 0 0 0 0 0 0 0 0 0.002 MAT 1 '
MAY 7-8 0.004 0.007 0 0 0 0 0 0 0 0 0.002 MAY 21-22 0.006 0.001 0 0 0 0 0 0 0 0 0.005 JUN 2-3 7.575 7.570 0.003 0 0 0 0 0 0 0 0.003 JUN 6-7 4.365 4.365 0 0 0 0 0 0 0 0 0 JUN 10-11 7.023 7.023 0 0 0 0 0 0 0 0 0 g JUN 14-15 5.843 5.818 0 0 0 0 0 0 0 0 0.025 JUN 18-89 28.513 28.500 0 0 0 0 0 0 0 0 0.013 JUN 22-23 24.875 24.805 0.054- 0 0 0 0 0 0 0 0.020 JUN 26-27 30.637 30.557 0.075 0 0 0 0 0 0 0 0. 00 5 JUN 30- 7.770 7.725 0 0 0 0 0 0 0 0 0.065 JUL 1 m a
Salem 316 (b) Demonstration
. ,m; 1
(/ TABLE 6.1-4 (page 2 of 4) Total Total Tarnet Species Densities pontarget Egg Say White Atlant1C 31ue b ac k Amer &can StrLped $pec ies Date Densities Anchove Weakfish Perch M Croaker Alewife Herring Shad Bass Densities 1980 JUL 4-5 28.415 28.365 0.015 0 0 0 0 0 0 0 0.035 JCL 8-9 9.170 9.165 0 0 0 0 0 0 0 0 u.005 JUL 12 13.890 13.710 0 0 0 0 0 0 0 0 0.175 JUL 16-17 26.185 26.175 0 0 0 0 0 0 0 0 0.010 JUL 20-21 65.228 65.223 0 0 0 0 0 0 0 0 0.005 JUL 26-25 7.965 7. % 0 0.005 0 0 0 0 0 0 0 0.020 JUL 28-29 8.210 8.180 0 0 0 -0 0 0 0 0 0.030 AUG t-2 27.892 27.M7 0 0 0 0 0 0 0 0 0.045 AUG 5-6 5.975 5.975 0 0 0 0 0 0 0 0 0 AUG 9-ti, 0.550 0.510 0 0 0 0 0 0 0 0 0.060 AUG 13 2.%7 2. %0 0 0 0 0 0 0 0 0 0.027 AUG 17-18 18.415 18.415 0 0 0 0 0 0 0 0 0 A'J G 21-22 0.100 0.095 0 0- 0 0 0 0 0 0 u.005
- AUG 25 0.040 0.027 0 0 0 0 0 0 0 0 0.013 AUG 29-30 1.035 1.030 0 0 0 0 0 0 0 0 0.0u5 Str 2-3 0 0 0 0 0 0 0 0 0 0 0 SEP 6 0 0 0 0 0 0 0 0 0 0 0 SEP 10-11 0.005 0.005 . -0 0 0 0 0 0 0 0 0 Str 14-13 0 0 0 0 0 0 0 0 0 0 0 stP 18 0 0 0 0 0 0 0 0 0 0 0 SEP 22 0 0 0 0 0 0 0 0 0 0 0 SEP 26-27 0 0 0 0 0 0 0 0 0 0 0 OCT.1 0 0 0 0 0 0 0 0 0 0 0 1981 MAY 7-8 0 0 0 0 0 0 0 0 0 0 0 MAY llat! 0.012 0.006 0 0 0 0 0 0 0 0 0.006 MAT 15-16 -0 0 0 0 0 0 0 0 0 0 0 MAY 23-24 0.035 0.020 0.005 0 0 0 0 0 0 0 0.010 MAY 27-28 0.010 0 0 0 0 0 0 0 0 0 0.010 Jun 22-23 3.704 3.682 0.002 0 0 0 0 0 0 0 0 020 -[]
( j JUN 26-27 7.295 7.285 0 0 0 0 0 0 0 0 0.010 v JUL t-2 5.354 5.300 0 0 0 0 0 0 0 0 0.054 JUL 4-5 ' 14.010 13.990 0 0 0 0 0 0 0 0 0.02C JUL 8-9 13.173 13.147 0.00 7 0 0 0 0 0 0 0 0.020 JUL 12-13 10.685 10.630 0.035 0 0 0 0 0 0 0 0.020 JUL 16-17 S.100 8.070 0.020 0 0 0 0 0 0 0 0.010 JUL 20-21 14.806 14.776 0.005 0 0 0 0 0 0 0 0.025 JUL 24-25 13.320 13.305 0 0 0 0 0 0 0 0 0.015 JUL 28-29 7.426 7.411 0.00 5 0 0 0 0 0 0 0 0.010 AUG t-2 9.520 8.730 0 0 0 0- 0 0 0 0 0.790 AUG 5-9 14.177 14.177 0 0 0 0 0 0 0 0 0 AUG 9-10 16. % 0 16.635 0 0 0 0 0 0 0 0 J.305 AUG 13-14 1.567 1. 5% C 0 0 0 0 0 0 0 0 . 0124 AUG 17*18 1.255 1.215 0 0 0 0 0 0 0 0 0. 06 0 AUG 21-22 0.933 0.933 0 0 0 0 0 0 0 0 0 s w
. - - - . _ . , - . . . . . -- ,,__ ,, . - - - - - -..~,.-- ...- _ ,_ - _
Salem 316 (b) Demonstration n
'( \
L ./ ~ TABLE 6.1-4 (page 3 of 4) Total Total Tartet Species Densities Nontarget Egg Sa y White At lantic 51ueb ac k Ame ric an Scraped Spec te s Date Densities Anchovy Weakfish Perch S g Croaker _ Alewife Herring Shad Bass Densities 1951 (Cont.) AUG 25-26 0.025 0.020 0 0 0 0 0 0 0 0 0.005 AUG 29-30 0.255 0.255 0 0 0 0 0 0 0 0 0 stP 2-3 . 0.220 0.220 0 0 0 0 0 0 0 0 0 SEP 5 0.040 0.%0 0 0 0 0 0 0 0 0 0 527 10-11 0 0 0 0 0 0 0 0 0 0 0 SEP 14-15 0 0 0 0 0 0 0 0 0 0 0 SEP 14-19 0 0 0 0 0 0 0 0 0 0 0 str 22-23 0 0 0 0 0 0 0 0 0 0 0 SEP 26-27 0 0 0 0 0 0 0 0 0 0 0 str 30- - 0 0 0 0 0 0 0 0 0 0 0 OCT 1 0CT 3-4 0 0 0 0 0 0 0 0 0 0 u OCT 4-9 0 0 0 0 0 0 0 0 0 0 0 OCT 12-!J 0 0 0 0 0 0 0 0 0 0 0 OCT 16-17 0 0 0 0 0 0 0 0 0 0 0 OCT 20-21 0 0 0 0 0 0 0 0 0 0 0 OCT 24-25 0 0 0 0 0 0 0 0 0 0 0 OCT 28-29 0 0 0 0 0 0 0 0 0 0 0 1982 MAY 4 0.033 0 0 0 0 0 0 0 0 0 0.033 MAY 10-11 0.015 0.015 0 0 6 0 0 0 0 0 0 MAY 13-14 0 0 0 0 0 0 0 0 0 0 0 MAY 17-18 0.025 0.025 0 0 0 0 0 0 0 0 0 MAY 20-21 0.030 0.030 0 0 0 0 0 0 0 0 0 MAY 24-25 0.050 0.045 0 0 0 0 0 0 0 0 0.005 MAY 27-28 0.285 0.285 0 0 0 0 0 0 0 0 0 MAY 11 0.565 0.565 0 0 0 0 0 0 0 0 0 JUN l' Km 4-5 0.290 0.290 - 0 0 0 0 0 0 0 0 0 [',} JUN 0-9 2.590 2.590 0 0 0 0 0 0 0 0 0 RN 12-13 0.920 0.920 0 0 0 0 0 0 0 0 0 JUN 16-It 0.435 0.435 0 0 0 0 0 0 0 0 0 W N 20-28 0.365. 0.365 0 0 0 0 0 0 0 0 0 A N 28-29 0' 0 0 0 0 0 0 0 0 0 0 JUL 2-3 7.455 7.455 0 0 0 0 0 0 0 0 0 TJL 7-8 0.625 0.625 0 0 0 0 0 0 0 0 0 TJL 10-11 3.425 3.230 0.195 n 0 0 0 0 0 0 0 nL 14-15 6.445 6.445 0 0 0 0 C 0 0 0 0 A L 19-20 1.405 - 1.365 0 0 0 0 0 0 0 0 0. N o KL 22-23 0.090 0.090 '0~ 0 0 0 0 0 0 0 o K L 26-27 _0.300 0.300 'O O O O 0 0 0 0 0 JUL 30-31 0.405 0.405 0 0 0 0 0 0 0 0 0 AUC 3-4 0.d95 -0.895 0 0 - "' - - - - - - AUG 9-10 . 0.195 0.195 0 0 - - - - - - 5 AUG 11-12 2.410 2.410 0 0 - - - - - . AUG !$-16 0.035 - 0.035 0 0 - - - - - - AUG 19-20 0.040 0.040 0 0 - - - - ia) Samples were analysed only for bay anchovy, weakfish, and white perch after this date, e di I rs i ()
d Salem 316 (b) Demcastration , N. TABLE 6.1-4 (page 4 of 4) , 4 Total Total Taraet Species Densities tiontarget C;g Bay M te Aslantic Stueesch American Sc r a ped Species Dat e Densities Anchovy ide ak f ish Perch M Croeker Alewife Herrina Shad Bass Densities 1992 (Cont.) AtJG 23-24 'O O O O - - - - - - AL'G 17-28 0.100 0.095 0.005 0 - - - - - - - SEP 1-2 0 0 0 0 - - - - - - - SEP 4-5 0 0 0 0 - - - - - - - SEP 8-9 0.005 0.005 0 4 - - - SEP 11-12 0 0 0 0 - - - - - - . SEP 16-17 0.010 0.010 0 0 - - - - - - - SEP 20-28 0 0 0 0 - - - - - SEP 24-25 0 'O O C - - - - Str 28-29 0 0 0 0 - - - - - - - 1 OCT 2-3 0 0- 0 0 - - - - - - OCT 6-7 0 0 0. 0 - - - - - 0CT +-10 0 0 0 0 - - - - - - OCT 15 0 -0 0 0 - - - - - OCT 20-21 0 0 0 0 - - - OCT 22-23 0 0 0 0 - - - - OCT 27-28 0 0 0 0 - - - - - OCT 30-3! 0 0 0 0 - - - - s 3*
.1 4
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Salem 316 (b) Demonstration /~'N i J 3 V TABLE 6.1-5 ESTIMATED LARVAL ENTRAINMENT DENSITIES (No./m ) 0F FISH SPECIES AT THE SALEM GENERATING STATION FROM ENTRAINMENT ABUNDANCE PROGRAM (1977-1982) Total Total tartet Speeles Densities Montarget Larval Say 'hite
= Atlantic 8L ue bac k Americam St r iped Species Date , Densities Anchovv Weakfish Perch M Croaker Alewife Herrina Shad Bass Densities 19'1 AUG 3t- 0.659 0.574 0 0 0 0 0 0 0 0 0.065 itP 1 DEC 7-8 0 0 0 0 0 0 0 0 0 0 0 1978 PES 27-28 0 0 0 0 0 0 0 0 0 0 0 MAR 2-3 0.005 0 0 0 0 0 0 0 0 0 0.005 MAA 16-17 0 0 0 0 0 0 0 0 0 0 0 APR 19-20 0.003 0 0 0 0 0 0 0 0 0 0.003 JUN 29-29 2.618 2.134 0.102 0 0 0 0 0 0 0 0.410 J7L 12-11 7.352 6.146 0.554 0 0 0 0 0 0 0 0.e52 JUL 27-28 4.970 4.197 0.017 0 0 0 0 0 0 0 0.75?
ACC 10-L1 1.968 1.080 0.013 0 0 0 0 0 0 0 0.s79 AUG 31- 0.383 0.343 0 0 0 0.005 0 0 0 0 0.03s SEP L SEP 13 14 0.055 0.042 0 0 0 0.003 0 0 0 0 0.010 OCT Lt 0.011 0.011 0 0 0 0 0 0 0 0 0 NOV L-2 0.003 0 0 0 0 0 6 0 0 0 0.003 NOV 21-22 0.001 0 0 0 0 0 0 0 0 0 0.001 DEC 13 0 0 0 0 0 0 0 0 0 0 0 1979 J"N e-7 0.106 0.068 0.015 0 0 0 0 0 0 0 0.023 JUL 5-6 2.484 1.261 0.037 0 0 0 0 0 0 0 t. Lee JUL 12-13 3.593 2.584 0.029 0 0 0 0 0 0 0 0.981 JUL 19-20 6.381 5.932 0.154 0 0 0 0 0 0 0 0.296 J'd 25-26 2.933 2.338 0.008 0 0 0 0 0 0 0 1.173 h AUG 22-23 OCT 17-18 1.373 f.004 0.833 0.005 0 0 0 0 0 0 C 0 0 0 0 0 0 0 0 0 0.539 0.003 k V OCT lt- 0 0 0 0 0 0 0 0 0 0 0 NOV 1 _ 1963 JAN 21-24 0 0 0 0 0 0 0 0 0 0 0 MAR 14-20 0 0 0 0 0 0 0 0 0 0 3 472 16-17 0.022 0 0 0.017 0 0 0 0 0 0 0.00. APR 30- 0.002 0 0 0 0 0 0 0 0 0 0.002 MAY l MAY 7-9 0.003 0.001 0 0 0 0 0 0 0 0 0.002 MAY 21-22 0.088 0.009 0.060 0- 0 0 0 0 0 0 0.019 JUN 2 1.748 t.488 0.180 0 0 0 0 0 0 0 0.081 JUN 6-7 0.275 0 148 0.103 0 0 0 0 0 0 0 0.026 JUN 10-It 0.683 0.450 0.023 0 0 0 0 0 0 0 0.210 JUN 14-15 1.130 0.825 0.053 0 0 0 0 0 0 0 J.255 JUN 18-19 1.900 0.693 0.020 0 0 0 0 0 0 0 u.187 JUN 22-23 640 0.265 0.050 0 0 0 0 0 0 0 0.325 JUN 26-27 4 588 0.525 0 0 0 0 0 0 0 0 . 04 JUN 30- 3.300 1.860 0.010 0 0 0 0 0 0 0 1.633 JCL 1 / O 4 \._/
Salem 316 (b) Demonstration p) t
'v' TABLE 6.1-5 (page 2 of 4)
Total Total Target Species Densities Nontarget Larval Sa y White Atlantic Bluecac a Ame r tc an scriped Species Date . Densities Anchowy Weakfish Perch g Croaker Alewife Merring Shad Sass Densities 1980 JUL 4-5 2.960 .1.290 0.065 0 0- 0 0 0 0 0 1.605 JUL 8-9 26.190 24.230 0.700 0 '0 0 0 0 0 0 1.260 JUL 12-13 4.555 3.740 0.200 0 0 0- 0 0 0 0 0.615 JUL'16-17 7.755 6.300 0.000 0 0 0 0 0- G 0 1.375 JUL 20-21 5.Mt 4.106 0.104 - 0 0 0 0 0 0 0 1.451 JUL 24-25 10.285 8.960 0.075 0 0 0 0 0 0 0 1.250 JUL 28-29 3.925 3.035 0.040 0 0 0 0 0 0 0 0.530 AUG 1*2 - 8,M9 6 .99 6 0 0 0 0 0 0 0 0 1.67e AUG 5-6 3.915 3.410 0.005 0 0 0 0 0 0 0 0.500 AUG 9-10 3.325 2.910 0 0 0 0 0 0 0 0 0.415 AUG 13 2.447 1.287 0 0 0 0 0 0 0 0 1.160 AUG 17-18 1.430 0.645 0 0 0 0 0 0 0 0 0.785 AUG 21-22 0.829 0.574 0 0 0 0 0 0 0 0 0.255 AUG 25 0.477 0.435 0 0 0 0 0 0 0 0 0. 362 AUG 29-30 0.455 0.265 0 0 0 0 0 0 0 0 0.190 SEP 2 0.740 0.180 0 0 0 0 0 0 0 0 0. 060 SEP 6 0.480 0.467 0 0 0 0 0 0 0 0 0.013 StP 10-11 0.355 0.275 0 0 0 0 0 0 0 0 0.080 SEP 14-15 0.115 0.095 0 0 0 0 0 0 0 0 0.020
'stP 18 0.270 0.140 0 0 0 0 0 0 0 0 0.130 LstP 22 0.047 0.033 0 0 0 0 0 0 0 0 0.013
$EP 26-27 0 0 0 0 0 0 0 0 0 0 0 OCT I 0.010 0.010 0 0 0 0 0 0 0 0 0 1981 MAY 7-8 0.030 0 0 0 0 0 0 0 0 0 0.039 MAT (1-12 0.478 0 0 0 0 0 0 0 0 0 0.475 MAf 15-16 0.045 0 0 0 0 0 0 0 0 0 0.065 MAY 23-24 0.020 9. 0 0 0 0 3 0 0 0 0.020 MAY 27-28 0.050 0 0 0 0 0 0 0 0 0 0.050 JUN 22-23 4.470 1.572 0.015 _ 0 0 0 0 J 0 0 4.884 s
0.275 0 0 0 0 0 0 0 u.095
. (j JUN 26-27 0.370 0 0 0 0 0 0.30 JUL t-2 1.364 0.993 0.007 0 0 0 JUL 4-5 L.670 0.685 0.040 0 0 0 0 0 0 0 0.965 J'JL 8-9 1.427 0.953 0.040 0 0 0 0 0 0 0 0.434 JUL 12-13 1.330 1.060 0.005 0 0 0 0 0 0 0 0.205 JUL 16-17 11.975 1.695 0.005 0 0 0 0 0 0 0 0.275 JUL 20-21 11.493 10.664 0.088 0 0 0 0 0 0 0 0.6-6 JUL 24-25 3.625 3.22 0 0.020 0 0 0 0 0 0 0 0.3s5 JVL 20-29 L.854 1.437 0.030 0 0 0 0 0 0 0 0.3a7 AUG 1-2 0.385 0.245 0 0 0 0 0 0 0 0 0.140 AUG 5-6 2.570 1.479 0 0 0 0 0 0 0 0 1.092 AUG 9-10 1.780 1.060 0.010 0 0 0 0 0 0 u 0. ?!U AUG 1)*14 3.173 3.048 0 0 0 0 0 0 0 0 0.124 AUG 17-18 1.135 0.785 . 0.010 0 0 0 0 0 0 0 0. leo AUG 2;-22 0.607 0.480 0 0 0 0 0 0 0 0 0.126 f%., ^
l
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W Salem 316 (b) Demonstration OV TABLE 6.1-5 (page 3 of 4) Total total Tartet $pecies Densities Montarget Larval say Whtte Atlant&c Blueteck Ame r tc an Scraped Species Date tre s s it ies Anchovy Weakfish Perch g Croaker Alewife Herring Shad Bass Deneities 194 6 (Conc.) AUG 25-26 ~0.440 0.440 - 0 0 0 5 0 0 0 0 0.040 AUG 29-30 0.335 0.295 - 0 0 0 0 0 0 0 0 0.060
$17 2-3 0.205 - 0.175 0 0 0 0 0 0 0 0 0.030 SEF 5 0.133 0.113 0 0 0 0 0 0 0 0 0.020 SEP 10-11 . 0.227 . G.213 A 0 0 0 0 0 0 0 0.013 SEP 14-15 0.315 - 0.305 0 0 0 0 0 0 0 0 0.010
$1P 18-19 0.295 0.285 0 0 0 0 0 0 0 0 0.010 SEP 22-23 0.275 0.275 0 0 0 0 0 0 0 0 0 stP 26-27 0.045 0.045 0 0 0 0 0 0 0 0 0 SEP 3D- 0.060 0.035 0 0 0 0.025 0 0 0 u o OCT I 0CT 3-4 0.04u 0 0 0 0 0.040 3 0 0 0 0 Oct 4-9 0.005 0.005 0 0 0 0 0 0 0 0 0 OCT 12-13 0.015 0.005 0 0 0 0.010 0 0 0 0 0 OCT 16-17 . 0.005 0 0 0 0 0.005 0 0 0 0 0 OCT 20-21 0.030 0.025 0 0 0 0.005 0 0 0 0 0
.0CT 24-25 0 0 0 0 0 0 0 0 0 0 0 OCT 28-29 0.015 0.005 0 0 0 0 0 0 0 0 0.010 1982 MAY 4-5 0.073 0 0 0.067 0 0 0 0 0 0 0.007 MAY (0-11 0.020 0.005 0 0.005 0 0 0 0 0 0 0.010 MAY L3-16 0.070 0 0 0 0 0 0 0 0 0 0.070 MAY 17-18 0.015 0 0 0 0 0 0 0 0 0 0.065 MAY 24-25 0.005 0 0 0 0 0 0 0 0 0 0.005 MAY 27-28 0.225 0.145 0.051 0 0 0 0 0 0 0 0.u25 MAY 31- 0.140 0.015 0.055 0 0 0 0 0 0 0 0.070
- JUN 1 JUN 4-5 0.380 0.255 0.085 0 0 0 0 0 0 0 0.04 0 JUN 8-9 0.475 0.420 0.025 0 0 0 0 0 0 0 0.030
; JVN 12-13 2.605 2.340 0.025 0 0 0 0 0 0 0 0.240
.\v} JUN 16-t?
JUN 20-21 0.335 1.565 0.170 0.74 5 0.015 0 0 0 0 0 0. 0 0 0 0 0 0 0 0 0 0.165 0.805 JUN 28-29 0.485 0.318 0.017 0 0 0 0 0 0 0 0.150 JCL 2-3 3.240 2.255 0.195 0 0 -0 0 0 0 0 0.790 J'J L 7-8 6.565 4.195 0.025 0 0 0 0 0 0 0 2.345 JUL 10-11' 6.030 5.125 0.015 0 0 0 0 0 0 0 0.890 JL'L I4-15 4.220 3.330 0.015 0 0 0 0 0 0. o 0.875-JUL 19-20 1.815 4.645 0.010 0 0 0 0 0 0 0 1.160 JUL 22-23. 2.425 1.975 0.005 0 -0 0 0 0 0 0 0. 4e 5 JUL 26-27 1.050 0.845 0 0 0 0 0 0 0 0 0.205 JUL 30-31 0.335 0.380 0 0 O o 0 0 0 o u.005 AUG 3-4 1.345 1.345 0 0- -g - - - - - - AUC 9-80 1.54 5 1.54 5 0 0 - - - - - - - AUG 11-12 " 0.790 0.790 0 0 - - - - - - - AUG 15-16 0.395 0.395 0 0 - - - - - .. - AUG 19-20 0.185 0.185 0 0 - . - - - - - Ial Samples wre analyzed oaty for bay anchovy , weakfish, and white perch af ter this date. 9
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i - . TABLE 6.1-5 (page 4 of 4) i 2 Total Total Tartec species Densities hontarget 1.arvel Say White Atlantic Blueback June ric an StrLped $pec ie s
- Date Densities Anchovy Weakfish Perch g Croaker Alewife Herring Shad Sass Censities ,
- 1982 (Coet.)
AUG 23-24 .0.630 0.630 0 0 - - - - - - - AUG 27-28 0.240 0.240 0 0 - - - - - - - . .$EP l 2 0.110 0.110 0 0 - - - - - - - SEP 6-4 0.125 . 0.115 0.010 0 - - - - - - - 4 $EP 8 0.130 0.130 0 0 - - - - - - - - SEP !!-12 0.050 0.050 ' 0 0 - - - - - - - ., SEP 16-17 'O.070 0.070 0 0' = - - - - - - SEP 20-21 0.025 0.015 0 0 - - - - - - - - SEP 2*-25 0.010 0.010 0 0 - - - - - - - SEP 28-29 0.020. 0.020 0 0 - - - - - - -
-- OCT 2-3 0.065 0.065 0 0 - - - - - - -
OCT 4-7 0.030 0.030 0 0 - - - - - - - OCT 9-10 0.815 0.115 0 0 - - - - - - - e OCT IS 0.040 0.040 0 0 - - - - - - -
. OCT 2C-21 0 0 0 0 - - - - - -
- OCT 22-23 0.005 ' O.005 0 0 - - - - - - -
OCT 27-23 0 0 0 0 - - - - - - - OCT 10-31 0 0 0 0 .- - - - - - - i h J
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Salem 316 (b) Demonstration Cl TABLE 6.1-6 (page 3 of 4) Total Total Target species Densities Montarget Juvenile s Ba y White At l an t &c 81ue DaC h AmerLean St r 6 Ped spectes Date Densities Anchevy weakfish Perch g Croaker Alewste eterrent _ shed less Densittes 1981 (Cont .) AUG 25-26 0.400 0.370 0 0 0 0 0 0 0 0 0.030 AUG 29-30 0.080 0.082 0 0 0 0 0 0 0 0 0 SEP 2-1 0.110 0.105 0 0 0 0 0 0 0 0 0.005 SEP 5 0.040 0.033 0 0 0 0 0 0 0 0 0.007 ser 10-Il 0.067 0.06 7 0 0 0 0 0 0 0 0 0 5tP '4-15 0.150 0.145 0 0 0 0 0 0 0 0 0 . 00 5 SEP 18-19 0.045 0.04 3 0 0 0 0 0 0 0 0 0 4tP 22-23 0.140 0.135 0 0 0 0 0 0 0 0 0.wS stP 26-27 0.024 0.025 0 0 0 0 0 0 0 0 0 SEP 30- 0.135 0.115 0 0 0 0 0 0 0 0 0.020 OCT 1 OCT 3-4 0.160 0.160 0 0 0 0 0 0 0 0 0 0CT 8-9 0.040 0.040 0 0 0 0 0 0 0 0 0.005 3CT 12-13 0.070 0.070 0.- 0 0 0 0 0 0 0 0 OCT 16-17 0.030 0.025 0 0 0 0.005 0 0 0 0 9 OCT 20-!! 0.080 0.075 0 0 0 0 0 0 0 0 0.005 0CT 24-25 0.085 0.060 0.005 0 0 0.015 0 0 0 0 0.005 oCT 28-29 0.044 0 0 0 0 0 0 0 0 0 0 1982 MAY .-5 0 0 0 0 0 0 0 0 0 0 0 MAY 10-11 0.095 0.005 0 0 0.090 0 0 0 0 0 0 MAY t3-14 0.225 0 0 0 0.279 0 0 0 0 0 0. Dul MAf 17-18 0.235 0 0 0 0.235 0 0 0 0 0 0 MAY 20-21 0.380 0 0 0 0.360 0 0 0 3 0 0.020 MAf 24-25 0.170 0 0 0 0.150 0 0 0 0 0 0.020
*AY 27-28 0.145 0 0 0 0.240 0 0 0 0 0 0.005 MAY 31- 0.085 0 0 0 0.C75 0 0 0 0 0 0.010 J:NL J'JN 4-5 0.125 0 0 0 0.110 0 0 0 0 0 0.015 f JUN 8-9 0.025 0 0 0 0.015 0 0 0 0 0 0.010
[m ( ,/
\ JUN 82-13 JU3 16-17 0.195 0.145 0
0 0.035 0.065 0 0 0.150 0.080 0 0 0 0 0 0 0 0 0 0 0.010 0.020 JUN 20-21 0.195 0 0.085 0 0.100 0 0 0 0 0 0.010 JUN 28-29 0.085 0 0.030 0 0.020 0 0 0 0 0 0.010 J;L 2-3 0.100 0.025 0.020 0 0.005 0 0 0 0 0 0 TJL 7-8 0.375 0.075 0.005 0 0.010 0 0 0 0 0 0 12L 10-11 0.095 0.360 0.005 0 0.005 0 0 0 0 0 0 JJL te-15 0.110 0.085 0.030 0 0 0 0 0 0 0 9
.JL 19-20 0.080 0.075 0.005 0 0 0 0 0 0 0 >
';L 22-23 0.025 0.075 0 0 0 0 0 0 0 0 v JUL 24-27 0.04 0 0.025 0.005 0 0 0 0 0 0 0 o J L 30-31 0. 2% 0.035 0.025 0 0 ,3 0 0 0 0 o u LUG 3-4 0.095 0.225 0.010 0 -4 - - - - - -
AUG 9-10 0.195 0.085 0.005 0 - - - - - - - AJG 11-t2 0.320 0.190 0.010 0 - - - - - - - AUG 15*l6 0.340 0.340 0 0 - - - - - - - Arc 19-20 0.030 0.030 0 0 - - - - - - - Til samples were anatyred octy for bay anchovy, we ektish, and white perch af ter this date. jf 'a
Salem 316 (b) Demonstration
/~
t j ) TABLE 6.1-6 (page 4 of 4) Tetet , Tete! Teraet Species Densities heeterget Juvenilee Bay Wite Atlanthe Bluebec k Americea Stripee Species _Oate Denetties Anchevy Weekfish Perch M Creeher Alewife Herrina Shed Sees Densities ISa2 (coat.3 AUG 23-24 0.000 0.000 0 0 . . . . . . . AUG 27*20 D.MO 0.h4 0 0 . . . . . . . SSP I.2 0.MS 0.MS 0 0 . . . . . . . SEP 4 5 0.25 0.he 0.00S 0 . . . . . . . SEP 0 9 0.050 0.MS 0.005 0 . . . . . . . SEP ll*!! 0.030 0.030 0- 0 . . . . . . . SEP 1617 0.070 0.050 0.020 0 . . . . . . . SEP 20 21 0 0 0 0 . . . . . . . SOF 26 25 0.h5 0.035 0.014 0 -. . . . . . . SEP 20-29 0.060 0.055 0.005 0 . . . . . . . OCT 2 3 0.039 0.035 0.005 0 . . . . . . . OCT 4 7 0.010 0.010 0 0 . . . . . . . OCT 9 10 0.020 0.020 0 0 . . . . . . . OCT IS 0.033 0.033 0 0 . . . . . . . OCT 20 21 0.025 0.025 0- 0 . . . . . . . OCT 22 23 0.075 0.075 0 0 . . . . . . . OCT 27 20 0.M0 0.M0 0 0 . . . . . . . OCT 30 31 0 0 0 0 . . . . . . . r i i A l
Salem 316 (b) Demonstration TABLE 6.1-7 ESTIMATED ADULT ENTRAINMENT DENSITIES (No./m ) 0F FISH SPECIES AT THE SALEM GENERATING STATION FROM ENTRAINMENT ABUNDANCE PROGRAM (1977-1982) Total Total Tarset Ssecles Densities katarget Adult Sa y Whste Atlantic St uetac k Aperscan Scraped Species Date Densities Anchevv ,4*akfleh Perch g Croaker Alkwife Herring $had lass . Demstates 1977 AUG 31- 0 0 0 0 0 0 0 0 0 0 0 SEP 1 OEC 7-8 0 0 0 0 0 0 0 0 0 0 0 19?$ FE9 27 0 0 0 0 0 0 0 0 0 0 0 MAA 2-3 0 0 0 0 0 0 0 0 0 0 0 MAR 16 0 0 0 0 0 0 0 0 0 0 0 APR 19-20 0.003 0 0 0 0 0 0 0 0 0 0.003 J'JW 29-29 0.020 0.018 0 0 0 0 0 0 0 0 0.002 JUL 12-13 'O.043 0.038 0 0 0 0 0 0 0 0 0.005 JUL 27-28 0.012 0.012 0 0 0 0 0 0 0 0 0 AUC 10-11 0.035 0.032 0 0 0 0 0 0 0 0 0.00* AGO 31- 0.004 0.002 0 0 0 0 0 0 0 0 0.002 StP 1 SEP 13-16 0.085 0.085 0 0 0 0 0 0 0 0 0 OCT 11 0.004 0.004 0 0 0 0 0 0 0 0 0 NOV 1 0.002 0 0 0 0 0 0 0 0 0 v.uu2 NOV 21-22 0 0 0 0 0 0 0 0 0 0 0 3tc 13 0 0 0 0 0 0 0 0 0 0 0 1979 JCM 6-7 0.010 0.003 0 0 0 0 0 0 0 0 0.008 JUL 5-6 0.011 0.002 0 0 0 0 0 0 0 0 0.009 JVL 12-13 0.002 0 0 0 0 0 0 0 0 0 0.002 JCL 19-20 0.003 0.002 0 0 0 0 0 0 0 0 0.uu2 JUL 25-26 0.002 0 0 0 0 0 0 0 0 0 0.002 p AUG 22*23 0.003 0 0 0 0 0 0 0 0 0 0. 0% t CCT 17-18 0.008 0.007 0 0 0 0 0 0 0 0 0.002 \ JCT li- 0 0 0 0 0 0 0 0 0 0 0 mw 1 1940 JAN 23-24 0 0 0 0 0 0 0 0 0 0 J MAR 19-20 0.004 0.005 0 0 0 0 0 0 0 u u.003
'APR 16-17 0.006 0.004 0 0 0 0 0 0 0 0 0.u02 APR 30- 0.068 0.068 0 0 0 0 0 0 0 0 0 MAY l MAY 7-8 0.295 0.292 0 0 0 0 0 0 0 u 9.0u3 MAY 21-22 0.141 0.141 0 0 0 0 0 0 0 0 u JCN 2-3 0.023 0.025 0 0 0 0 0 0 0 u U. 00 3 JUN 6*7 0.223 0.220 0 0 0 0 0 0 0 0 0.003 JCM 10-Il 0.46 7 0.86 7 0 0 0 0 0 0 0 o u JUN 14-15 0.140 0.140 0 0 0 0 0 0 0 4 0 JUN 18-19 0.140 0.140 0 0 0 0 0 0 0 0 a JUN 22 23 0.075 0.075 0 0 0 0 0 0 0 v 0 JUN 26-27 0.250 0.050 0 0 0 0 0 0 0 0 J JON 30- 3.045 0.045 0 0 0 0 0 0 0 0 u JCL 1 7
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oene 0eme}3}es yvsgoaA nee 4}}84 d*234 5 oa 3Joeg1ea ygen};e me44}us sgep gees geus}atse 3 1690 )3*=8*( tni 9-5 0*090 0*090 0 0 0 0 0 0 0 0 0 tni 0-6 0'010 0*010 0 0 0 0 0 0 0 0 0 fA1 lE-1( 0*090 0*090 0 0 0 0 0 0 0 0 0 tni 19-14 0*020 030 0 0 0 0 0 0 0 0 0 i tQS 20-!! 0*015 0'015 0' 0 0 0 0 0 0 0 0 0 tsi I9-!5 01$ 0 015 0 0 '0 0 0 0 0 0 0 W 39-16 0'010 0* 0*010 0 0 0 0 0 0 0 0 0 VAD I-I 010 O*010 0 0 0 0 0 0 0 0 0 vaD 5-9 e'010 C* 010 0 0 0 O O O O O O YOD 6-10 0*020 0'0!O C* 0 0 0 0 0 0 0 0 0 voD lE 0*00( O*002 C 0 0 0 0 0 0 0 0 voD 11-18 0'090 0*0t5 0 0 0 0 0 0 0 0 0*005 Y00 21-!! llO 0*!05 0 0 0 0 0 0 0 0 0'005 VaD 25 0'009 0' 0 '5 0 0 0 0 0 0 0 0*009 voD !6-CO 0'035 0*035 -0 0 0 0 0 0 0 0 0 53d t-( 0*020 0'015 0 0 0 0 0 0 0 0 0'005 534 9 0'01( 0'01( 0 0 0 0 0 0 0 0 0 534 10-11 0 0 0 0 0 0 0 0 O O O
- SEJ 19-15 0*0tO 0*030 0 0 0 0 0 0 0 0 C*010 sad 18 0 0 0 0 0 0 0 0 0 0 0 834 ZZ 0 0 0 0 0 0 0 0 0 0 0 83d 29-ti 0 0 0 0 0 0 0 0 0 0 0 031 1 0 0 0 0 0 0 0 0 0 0 0 1681 hVA 4-9 0*095 0'095 0 0 0 0 0 0 0 ,O O EVA 11-13 0*19E 0*t91 0 0 0 0 0 0 O O O EVA 15-19' 0*010 010 0 0 0 0 0 0 0 0 0 bYA t(-39 0'010 0'010 0 0 0 0 0 0 0 0 0 WVA 21-88 0'010 0'010 0 0 0 0 0 0 0 0
/_\' fAK !!-I( 0'099 0'091-0 0 0 0 0 0 0 0 0 0 jp t tan 29-11 0*010 0'010 0 0 0 0 0 0 0 0 0 W 1-3 0 015 001$ 0 0 0 0 0 0 0 0 0 tni 9-5 O025 0*025 0 0 0- 0 0 0 0 0 0 W 8-6 0 0 0 0 0 0 0 0 0 0 0 tni lE-lC 0*020 0'CIO 0 0 0 0 0 0 0 0 0 W 19-14 0*010 0'040 0 0 0 0 0 0 0 0 0 tni 20-21 0*015 0*020 0 0 0 0 0 0 0 0 0'005 W 29-25 0'005 0'005 0 0 0 0 0 0 0 0 0 tni 18-t6 0*01$ D* 015 - 0 0 0 0 0 0 0 0 0 vnD 1-2 0'095 0*095 0 0 0 0 0 0 0 0 0 voD 5-9 0'098 0'091 0 0 0 0 0 0 0 0 0'001 yaD 6-10 0 0 0 0 0 0 0 0 0 0 0 VOD 1(-19 0 0 0 0 0 0 0 0 0 0 0 voD 14-18 0*010 0'0!O 0 0 0 0 0 0 0 0 0 voD 21-!! 0 0 0 0 0 0 0 0 0 0 0 f )V. .
5 1
~ . - . . . . , . - - . - - - - - . . - ,. .-. - -.._ .. .. . - . . ~ .
Salem 316 (b) Demonstration C(N' TABLE 6.1-7 (page 3 of 4) Total Totat Tarset Species Densities sentarget Adult Bay Whste Actantic Bluebeck hee r tc an Scraped $pecies _ jere Densities Anchovv Weakfish Alewife
. Perch g Croaker Herrina Shad Sass Densities 1981 (Cont.)
AUG 25-26 0.010 0.005 0 0 0 0 0 0 0 0 0.001 AUG 29-30 0 0 0 0 0 0 0 0 0 0 0
$CP 2-3 0 0 0 0 0 0 0 0 0 0 0 SEP 5 0 0 0 0 0 0 0 0 0 0 0
, ' SEP 10-11 0 0 0 0 0 0 0 0 0 0 0 SEP 14-11 0 0 0 0 0 0 0 0 0 0 0 SEP 18-19 0 0 0 0 0 0 0 0 0 0 0 SEP 22-23 0 0 0 0 0 0 0 0 0 0 0 SEP 26-27 0 0 0 0 0 0 0 0 0 0 0 stP 30- 0.035 0.035 0 0 0 0 0 0 0 0 0 OCT 1 OCT 3-4 0 0 0 0 0 0 0 0 0 0 0 OCT 8-9 0.011 0.015 0 0 0 0 0 0 0 0 0 OCT 12-13 0 0 0 0 0 0 0 0 0 0 0 oCT 16-17 0.005 0.005 0 0 0 0 0 0 0 0 0 OCT 20-21 0 0 0 0 0 0 0 0 0 0 0 OCT 24-21 0 0 0 0 0 0 0 0 0 0 0 OCT 28-29 '? ? 0 0 0 0 0 0 0 0 0 1982 MAY 4-5 0.020 0.020 0 0 0 0 0 0 0 0 0 MAY 10-11 0.020 0.020 0 0 0 0 0 9 0 0 0 MAY 13-14 0.020 0.020 0 0 0 0 0 0 0 0 0 MAY 11-18 0.005 0.005 0 0 0 0 0 0 0 0 0 MAY 20-2t 0.005 0.005 0 0 0 0 0 0 0 0 0 MAY 24-25 0.001 0.005 0 0 0 0 0 0 0 0 0 MAY 27-28 0 0 0 0 0 0 0 0 0 0 0 MAY 3t= 0.010 0.010 0 0 0 0 0 0 0 0 0 Ku 1 E4 4-5 0.015 0.015 0 0 0 0 0 0 0 0 0 n EN 8-9 0 0 0 0 0 0 0 0 0 0 0 l 1 WM 12-13 0.010 0.010 0 0 0 0 0 0 0 0 0
%*/ KN 16-!?
RN 20-21 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 Mit 28-29 0 0 0 0 0 0 0 0 0 0 0 RL 2-3 0.005 0.005 0 0 0 0 0 0 0 0 0 AL 7-6 0.005 0.005 0 0 0 0 0 0 0 0 0 W L 10-11 0.005 0.005 0 0 0 0 0 0 0 0 0 RL 14-15 0 0 0- 0 0 0 0 0 0 0 0 ML 19-20 0 0 0 0 0 0 0 0 0 0 0 KL 22-23 0 0 0 0 0 0 0 0 0 0 0 KL 26-27 0- 0 0 0 0 0 0 0 0 0 0 KL 30-31 0 0 0 0 Og ,3 0 0 0 0 0 0 AUG 3-4 0 0 0 0 - - * * * - AUG 9-10 0 0 0 0 - - - - - * - Acc 11-12 0 0 0 0 - - - - - - - AUG 15-16 0 0 0 0 - - - - - - - AUG 19 0 0 0 0 - - - - - - - (a) Samples were analysed only for bay anchovy, weakfish, and white perch af ter this date.
\ 'b
i. 4. t Salem 316 (b) Demonstratton i o TABLE 6.1-7 (page 4 of 4) Total a total Tarnet Species Densities Montarget Adult Say h te Atlantic Blueback Aperscan st r a ped Spec ies Date Densities Anchevy Weakflah Perch g Croaker Atewife Herrina Shad Sass Densities
! 1992 (Cont.)
AUG 23-24 0 0 0 0 - - . AUG 27-28 0 0 0 0 - - . . SEP l*2 0 .0 0 0 - - - . Sir 4-5 0 0 0 0 - - - . . - - SEP 8-9 0 0 0 0 - - . - -
. SEP 11 12 0 0 0 0 -
i SEP 16.!? 0 0 0 0 - - - - - SEP 20 28 0 0 0 0 - . - . . . 0.005 0.005 0 0 - . . . . . g SEP 24*25 -
$tP 28-29 0.005 0.005 0 0 . . - . - - .
OCT 2-3 0 0 0 0 - - - -
> OCT 6-7 0 0 0 0 - - . . - . - f OCT 9-10 0 0 'O O - . . . . . .
- - . l OCT IS 0 0 0 0 -
. OCT 20-21 0 0 0 0 - - - .
- OCT 22-23 0 -0 ^ 0' . 0 - - - . . - -
OCT 2?-2S 0 0 0 0 - . - - - OCT 30-31 0 0 0 0 - . . - - 3 5 Il a
,I 1
i i i i [ ] 4 ! i j- i + 4 4 4 5 4 . I-r k
- d. 1 5 .
[ - - f' p n 4 l ww- w~. .,v rm,. . ,,.4_m,, . , , _ _ . . . . , _ . ,, , _ , , _ - . . . . . . _ . . - . . . _ _ _ _,, _ __ - _ - . _ . - . - - . - . ~ . - - . . - - - - - . _ _ _ _ . . - - - _.
Salem 316(b) Demonstration _,m . - TABLE 6.1 COMPARISON OF Neomysis americana MEAN DENSITIES FOUND IN CIRCULATING WATER SYSTEM TO THOSE FOUND IN DELAWARE RIVER (rkm 64-97) Entraingent Riverrkm{64-97) Date (No./m ) (No./m ) 1979 MAR 27-30(,) 0.345 1.339 JUN 6-7 40.463 33.265 JUL 11-13 196.947 24.264 JUL 18-20 194.003 73.098 JUL 25-27 442.287 81.693 AUG 22-24 58.890 28.004 OCT 15-18 668.094 163.708 OCT 29-NOV 1 35.211 71.657 1980 MAR 17-20(,)) 29.563 34.468 APR 15-17(,. 0.169 0.780 APR 29-MAY 2
- 6.181 5.720 MAY 19-22 331.452 33.579 JUN 2-3 565.990 47.376 JUN 5-7 400.807 110.288 JUN 9-12 158.960 5.743
() . JUN 17-18 798.000 88.9.20 N' JUL 7-9 62.430 98.651 JUL 11-14 147.505 23.293 JUL 15-17 63.125 97.908 JUL 20-22 226.214 33.758 JUL 24-25 - 144.880 301.426 AUG 4-7 42.235 17.149 AUG 17-19 373.800 5.721 AUG 20-22 174.577 0.091 SEP 8-12 64.985 2.097 SEP 22-24 63.627 25.526 i Total 5290.740 1409.522 (a) NOV-APR Total 36.258 42.307 Seasonal E/R ratio = = 0.857 l3 MAY-0CT Total 5254.482 1367.215 5 Seasonal E/R ratio = = 3.843 6$2
.v
- __ . _ _ _ . _ _ , - _ - _ . - . _ - . _ _ _ _ _ _ _ . ~ , _ - _ - - - _ - - - _ _
Salem 316(b) Demonstration
'tb/ )
TABLE 6.1-9 "70JECTED MONTHLY ENTRAINMENT DENSITIES OF
.4eomysis americana BASED ON ESTIMATED RIVER DENSITIES AND E/R RATIOS Estimated Mean
- Projected Mean RiverDegsity Seasonal Entrainment3 Density Month (No./m ) E/R Ratio (No./m )
JAN 0.295 0.857 0.253 FEB 0.975 0.857 0.836 MAR 14.400 0.857 12.341 APR 2.722 0.857 2.333 MAY 11.737 3.843 45.105 JUN 69.661 3.843 267.707 JUL 51.723 3.843 198.771 AUG 38.756 3.843 148.939 SEP 54.649 3.843 210.016 OCT 50.364 3.843 193.549 NOV 31.987 0.857 27.413 DEC 9.170 0.857 7.859 (a) Mean river densities were estimated based on river abundance data collected between rkm 64 and 97 from 1974 through 1980. o)
Salem 316(b) Demonstration () TABLE 6.1-10 COMPARISON OF Gammarus tigrinus GROUP MEAN DENSITIES FOUND IN CIRCULATING WATER SYSTEM TO THOSE FOUND IN DELAWARE RIVER (rkm 64-97) Entrainmgnt Riverrkmg4-97 Date (No./m ) (No./m ) 1979 MAR 27-30(,) 12.996 4.369 JUN 6-7 28.668 1.639 JUL 11-13 16.236 0.324 JUL 18-20 26.727 1.313 JUL 25-27 31.144 1.411 AUG 22-24 2.950 0.306 OCT 15-18 3.457 0.716 OCT 29-NOV 1 5.647 2.726 1980 MAR 17-20((,) 3.495 2.361 APR 15-17 ,) 51.662 7.845 APR 29-(,) MAY 2 13.854 7.933 MAY 19-22 19.511 10.507 JUN 2-3 7.204 2.043 JUN 5-7 6.028 0.006 /l JUN 9-12 8.397 0.059
/ JUN 17-18 3.747 0.070 JUL 7-9 6.675 0.171 JUL 11-14 9.495 0.077 JUL 15-17 9.015 0.336 JUL 20-22 4.094 0.365 JUL 24-25 7.880 0.179 AUG 4-7 6.520 0.528 AUG 17-19 4.375 0.334 AUG 20-22 1.079 0.005 SEP 8-12 0.165 0.051 SEP 22-24 0.013 0.005 ,
' Total 291.034 45.688 (a) NOV-APR Total 82.007 22.508 Seasonal E/R ratio = = 3.643 l
MAY-0CT Total 209.027 23.180 9 Seasonal E/R ratio = 23;80 = 9.018 v
Salem 316(b) Demonstration TABLE 6.1-11 PROJECTED MONTHLY Gammarus tigrinus GROUP ENTRAINMENT DENSITY BASED ON ESTIMATED RIVER DENSITIES AND E/R RATIOS + Estimated Mean(a) Projected Mean . River Degsity Seasonal Entrainment3 Density Month (No./m ) E/R Ratio (No./m ) JAN 1.578 3.643 5.747 FEB 0.698 3.643 2.541 MAR 2.265 3.643 8.253 APR 5.927 3.643 21.591 - MAY 11.084 9.018 99.956
, JUN 1.359 9.018 12.252
( JUL 0.914 9.018 8.241
. AUG ~1.682 9.018 15.165 SEP 1.147 9.018 10.341 OCT 0.255 9.018 2.300 NOV 0.600 3.643 2.185 DEC 1.165 3.643 4.244 4
la) Mean river densities were estimated based on river abundance data collected between rkm 64 and 97 from 1974 through 1980. 4 ) i O p 7 --p-- g -g -- g y ,.ww r-e mgwy- ww ,1-Le9 -w gw-g w- - g , yy-wy,-r yp- yw y,mygp w gwygw y% y a a"v+r'wV'W-e wg
'-7M eNNN+~W&-h4M'? --w+9-e
- Salem 316 '(b) Dentonstratiort
/
-? i TABLE 6.1-12 PROJECTED WEEKLY ENTRAINMENT DENSITIES FOR SECONDARY TARGET SPECIES Deneities (No./100 mI) Densities (no./m Il Stuee se s Cates. Retring Alewife Spot i 8er (early (early American (early Atlantic Croeker Striped Bass peomysis Cammarus I Ween juveniles) juveniles) Sh ad juvenites) La rv ae Juventles Eggs La rv ae ame rsc ana spp.
! 0.0 0.0 0.0 0.0 0.v 0.29 0.0 0.0 0.25 5.75 2 0.0 0.0 0.0 0.0 0.0 0.33 0.0 0.0 0.25 5.75 3 0.0 0.0 0.0 0.0 0.0 0.38 0.0 0.0 0.25 5.75 4 0.0 0.0 0.0 0.0 0.0 0.40 0.0 0.0 0.25 5.75 5 0.0 0.0 0.0 0.0 0.0 0.34 0.0 0.0 0.58 3.91 4 0.0 0.0 0.0 0.0 0.0 0.25 0.0 0.0 0.83 2.54 7 0.0 0.0 0.0 0.0 0.0 0.15 0.0 0.0 0.83 2.54 8 0.0 0.0 0.0 0.0 0.0 0.06 0.0 0.0 0.83 2.54 9 0.0 0.0 . 0.0 0.0 0.0 0.0 0.0 0.0 7.41 5.80 10 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 12.34 4.25 11 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 12.34 3.25 11 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 12.34 8.25 13 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 10.91 10.16 14 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 2.32 21.59 15 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 2.33 21.59 16 0.0 0.0 0.0 0.0 0.0 0.0 1.6L 0.19 2.33 21.59 17 0.0 0.14 0.0 0.0 0.0 0.0 0.27 0.19 2.33 2t.59 18 0.0 0.09 0.0 0.0 0.0 0.0 0.13 0.14 39.02 88.76 19 0.0 0.0 0.0 6.20 0.0 0.0 0.35 0.34 45.10 99.96 20 0.17 0.03 0.0 20.57 0.0 0.0 0.35 0.40 45.10' 99.96 21 0 51 0.09 0.0 18.08 0.0 0.0 0.!! 0.19 45.10 99.96 22 0.0 0.0 0.0 18.08 0.0 0.0 0.0 0.05 153.28 62.37 23 0.12 0.0 0.0 5.92 0.0 0.0 0.0 0.07 267.70 12.25 24 0.08 0.0 0.0 18.00 0.0 0.0 0.0 0.04 267.70 12.25 /N 25 0.02 0.0 0.0 6.40 0.0 0.0 0.0 0.01 267.70 12.25 > 0.0 0.0 0.0 0.0 0.0 \
26 2.90 0.0 0.0 256.58 18.65 27 0.0 0.0 0.0 0.82 0.0 0.0 0.0 0.0 198.77 8.26 28 0.0 0.0 0.0 0'.07 0.0 0.0 0.0 0.0 198.77 8.2e 29 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 198.77 8.24 30 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 198.77 8.24 31 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 163.13 13.21 32 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 148.93 15.16 33 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 148.93 15.16 34 0.0 0.0 0.0 0.0 0.0 0.0 09 0.0 148.93 15.16 35 0.0 0.0 0.0 0.0 0.07 0.03 0.0 0.0 166.45 13.78 36 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 210.01 10.34 37 0.0 0.0 0.0 0.0 0.03 0.02 0.0 0.0 210.01 10.3. 38 - 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 210.01 10.34 39 0.0 0.0 0.0 0.0 0.36 0.0 0.0 0.0 210.01 10.34
.0 0.0 0.0 0.0 0.0 1.00 0.0 0.0 0.0 193.54 2.30 41 0.0 0.0 0.0 0.0 0.86 0.16 0.0 0.0 193.54 2.30 42 0.0 0.0 0.0 0.0 0.17 0.16 0.0 0.0 193.54 2.30 43 0.0 0.0 0.0 C.0 0.0 5.10 0.0 0.0 193.54 2.30 44 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 98.66 2.23 45 0.0 0.0 0.0 0.0 0.30 0.0 0.0 0.0 27.41 2.18 46 0.0 - 0.0 0.0 0.0 0.15 2.56 0.0 0.0 27.41 2.14 47 0.0 0.0 0.0 0.0 0.0 5.13 0.0 0.0 27.41 2.18 48 0.0 0.0 0.0 0.0 0.0 3.26 0.0 0.0 21.82 2.77
.9 - 0.0 0.0 0.0 0.0 0.0 1.40 0.0 0.0 7.85 4.26 50 0.0 0.0 0.0 0.0 0.0 0.17 0.0 0.0 7.85 4.24 51 0.0 0.0 0.0 0.0 0.0 0.19 0.0 0.0 7.85 4.24 52 C.0 0.0 0.0 0.0 0.0 0.24 0.0 0.0 7.85 4.24 53 0.0 0.0 0.0 0.0 0.0 0.26 0.0 0.0 7.85 4.24 I,,h .
v
S2152 316(b) Demonstration t p TABLE 6.1-13 PROJECTED WEEKLY ENTRAINMENT DENg1 TIES FOR () PRIMARY TARGET SPECIES (No./100m ) Bay Anchovy Calendar White Perch Juveniles Weakfish Week Prolarvae Postlarvae Eggs Larvae & Adults g Prolarvae Postlarvae Juv e n t l e's'
-1 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 2 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 3 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 4 0.0 0.0 0.0 0.0 0.10 0.0 0.0 0.0 0.0 5 0.0 0.0 0.0 0.0 0.09 0.0 0.0 0.0 0.0 6 0.0 0.0 0.0 0.0 0.06 0.0 0.0 0.0 0.0 7 0.0 0.0 0.0 0.0 0.04 0.0 0.0 0.0 0.0 8 0.0 0.0 0.0 0.0 0.01 0.0 0.0 0.0 0.0 9 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 10 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 11 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 12 0.0 0.0 0.0 0.0 0.70 0.0 0.0 0.0 0.0 13 0.0 0.0 0.0 0.0 0.61 0.0 0.0 0.0 0.0 L4 0.0 0.0 0.0 0.0 0.45 0.0 0.0 0.0 0.0 15 0.0 0.0 0.0 0.0 0.29 0,0 0.0 0.0 0.0 16 0.27 0.20 0.0 0.0 0.20 0.0 0.0 0.0 0.0 17 0.46 2.44 0.0 0.0 2.30 0.0 0.0 0.0 0.0 18 0.85 1.44 0.0 0.0 4.40 0.0 0.0 0.0 0.0 19 0.13 1.22 0.56 0.14 12.28 0.0 0.0 0.0 0.0 20 0.03 0.20 1.83 0.0 0.67 0.0 0.0 0.0 0.0 21 0.0 0.0 7.02 3.08 3.72 0.10 0.72 1.76 0.0 22 - 0.0 0.16 406.75 75.15 1.75 0.15 3.40 6.35 0.0 23 0.0 0.0 211.65 22.27 5.95 0.0 0.45 5.25 0.75 24 0.23 0.25 354.90 94.62 25.42 0.0 1.12 1.40 2.62 25 0.15 0.0 1154.64 68.60 5.72 1.04 0.60 1.50 5.74 gs.' 26 0.08 0.08 867.15 101.25 4.38 1.25 0.42 1.78 20.07 27 0.0 0.0 3546.f5 177.32 9.87 0.57 1.83 4.87 0.82 -
28 0.0 0.0 1156.10 660.21 7.44 3.56 14.39 7.30 4.27 29 0.0 0.0 1691.10 504.53 8.43 0.39 2.63 3.74 1.71 30 0.0 0.0 604.99 343.60 9.50 0.14 0.77 1.94 2.09 31 0.0 0.0 1041.08 208.86 19.42 0.0 0.0 0.J 1.58 32 0.0 0.0 , 479.37 179.92 18.47 0.0 0.08 0.38 2.25 33 0.0 0.0 398.48 105.75 52.15 0.0 0.0 0.17 2.33 14 0.0 0.0 27.37 56.53 97.45 0.0 0.0 0.0 1.53 35 0.0 0.0 25.77 28.60 39.97 0.07 0.0 0.0 0.36
- 36 0.0 0.0 0.90 20.10 31.82 0.0 0.0 0.20 0.40 37 0.0 0.0 0.21 15.00 30.86 0.0 0.0 0.0 0.20 38 0.0 0.0 0.0 15.16 25.80 0.0 0.0 0.0 0.20 39 0.0 0.0 0.0 2.20 5.50 0.0 0.0 0.0 0.20 40 0.0 0.0 0.0 2.62 5.37 0.0 0.0 0.0 u.0 41 0.0 0.0 0.0 3.40. 5.22 0.0 0.0 0.0 0.0 42 0.0 0.0 0.04 1.40 6.24 0.0 0.0 0.0 0.0 43 0.0 0.0 0.0 0.25 11.50 0.0 0.0 0.0 0.25 44 0.0 0.0 0.33 0.0 6.00 0.0 0.0 0.0 0.07 45 0.0 0.0 0.24 0.0 5.28 0.0 0.0 0.0 0.05 46 0.0 0.0 0.09 0.0 4.02 0.0 0.0 0.0 0.02 47 0.0 0.0 0.0 0.0 3.30 0.0 0.0 0.0 0.0 48 0.0 0.0 0.0 0.0 1.70 0.0 0.0 0.0 0.0 49 0.0 0.0 0.0 0.0 0.10 0.0 0.0 0.0 0.0 50 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 51 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 52 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 53 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 s
O V
Salem 316(b) Demonstration b TABLE 6 1-1!+
SUMMARY
OF ENTRAINMENT HORTALITY: SPOT EARLY JUVENILE OPERATION HISTORY: NO OUTAGE
== ===.... :Nf 44I % 4i ef 90Af4LlfY (16-=========.
N3N * *= *
- U N I T 1**==* ===== UNIT 2=====
WEE 4 THE994L THI41%L 7174L THE*WAL TOTAL 1 23.59 0.00 23.60 0.00 23.60 2 23.59 1 3J 23.63 0 00 23.60 3 2J.51 1.30 23.60 0.00 23.60 4 23 59 3.33 23.60 0.00 23.60 5 23.59 J.00 23.63 0.00 23.60 6 23 58 3.33 23.60 0.00 23.60 1 23.59 0.00 23.60 0.00 23.60
$ 23 59 0.0J 23.60 0.00 23.60 9 23.59 0.0J 23 60 0.00 23. 60 10 23.59 0.03 23.60 0.00 23.60 11 23 59 3.00 23 60 0.00 23.60 12 23.59 0.00 23.60 0.00 23 60 13 23 59 3.J3 23 60 0.00 23.60 14 23.59 0.03 23 60 0.00 23.60 15 23.59 1.00 23.60 0.00 23.60 16 23.59 0.03 23.60 0.00 23.60 17 23 59 1.33 23.60 0.00 23.60 19 23 59 0.03 23.60 0.00 23.60 19 23.59 0.00 23.60 0.01 23.60 20 23.59 0.00 23.60 1.07 29.41 21 23.59 0.33 23.60 21.04 39.67 22 23.59 3.1+ 24.24 65.59 73. 71 <~N 23 23.59 7.19 29.54 9*.44 96.53 23.59 42.79 91.39 99.53
'(#) 24 25 23.59 25.12 61.21 70 36 99.97 99.98 1 26 23.!* 89.17 90.96 100.00 100.00 27 23 59 95 93 96.89 100 00 100 0c 29 23.59 99 . 74 99.80 100.00 100.00 29 23.59 100.00 100.00 100.00 100.00 30 23.59 100.00 100.00 100.00 100.00 31 23 59 99. 99 100 00 100 00 100 00 32 23 59 100 .30 100.00 100.00 100.00 33 23 59 99.99 99.99 100.00 100.00 34 23.59 19.91 99.93 100.00 100.00 35 23.59 99.94 99.91 100.00 100.00 36 23.59 99 . 13 99.31 100.00 100.00 37 23 59 81.53 85.89 100.00 100 00 39 23.59 42 9s 56.44 99.66 99.74 39 23.59 4.50 27.03 49.59 92.04 40 23.59 0 10 23.67 38.21 52.79 41 23.59 3 03 23 60 1 54 24. 77 42 23 59 0.03 23.60 0.00 23.60 43 23.59 0.00 23.60 0 00 23.60 44 23.59 0.03 23.60 0.00 23.60 45 23 59 3 33 23.63 0.00 23.60 46 23.59 0.00 23 60 0.00 23.60 47 23 59 0.00 23.60 0.00 23.60 44 23.59 0.03 23.60 0.00 23.60 49 23 59 ).33 23.60 0.00 23.60 5J 23.59 0.0J 23.60 0.00 23.60 51 23.59 3.00 23.60 0.00 23.60 52 23.51 0.00 23.60 0.00 23.60 53 23.59 0.30 23 65 0.00 23.60 CHLORINE PORTAL!ff: 6.251 A v
i Salem 316(b) Demonstration
SUMMARY
OF ENTRAINMENT MORTALITY: BLUEBACK HERRING EARLY JUVENILE TABLE 6'.1-13 ("%) OPERATION HISTORY: NO OUTAGE - LOW MORTALITY ESTIMATES
...........cgrRArg1Est goaf4LITV tas...........
-..*-dNIf 1**..- **..*U1tf 2...=.
Nov TOTAL THtqMaL 'OTAL THE* MAL d!E4 T HE R M A L 25 94 3 01 25 94 0 00 25.94 1 25.94 0.00 25 94 0.00 25.94 2 3 25 94 0.00 25 94 0.00 25 94 1 00 25 94 0.00 25.94 4 25 94 25.94 5 25 94 3 03 25 94 3.J5 0.00 25.94 0.00 25.94 6 25 94 25.94 7 25 94 0 00 25 94 0 00 0.00 25 94 0.00 25.94 9 25 94 25.94 9 25.94 3 03 25 94 1 00 0.00 25 94 0.00 25.94 10 25.94 25.94 11 25 94 0.00 25 94 0.00 3 03 25.94 0 00 25 94 12 25 94 25.94 13 25.94 0.00 25.94 0.00 25.99 0 00 25 94 0.00 25.94 14 0.00 25.94 15 25 94 0 00 25.94 25 94 3 33 25.94 0 00 25.94 16 0 01 25 94 17 25.94 0.00 25.94 25 94 0 00 25 94 0 00 25.94 la 25 94 0.00 25.94 0 00 25.94 19 25 94 25.94 3 03 25 94 0 00 23 25.95 21 25.94 0 00 25.94 0.02 25.94 0.02 25 95 0 14 26 04 22 0.55 26 35 23 25.94 0.08 26.00 26.11 1 30 26.90 24 25.94 0 23 3 38 28 44 7s 1 25 25.94 0 . 75 26.49 28.06 T.36 32 87
%/ 26 25.94 2 86 34 27 27 25.94 3 47 29 53 11 25 8.51 32.24 22 08 42 29 29 25.94 57.21 29 25 94 21 31 41.72 42 23 19.27 40.21 39.62 55 28 30 25 94 52.71 31 25.94 16.87 38 43 36.14 25.94 21 32 41.73 42.42 57.35 32 53 88 33 25 94 18.06 39.31 37.72 33.65 21.64 44.93 34 25.94 10.41 35 25 94 11 73 34.61 27.96 46.64 31.57 20.16 40.87 36 25 94 7.61 30.50 37 25.94 1 62 27.13 6.16 l
26.29 2.30 27.64 I 38 25.94 0.48 26.22 39 25.94 3 05 25.94 0 38 25 94 0.01 25 94 0.05 25.97 40 l 25.94 0.00 25.94 0.00 25.94 41 0 00 25.94 42 25.94 3 00 25 94 l 0.00 25.94 0.00 25.9% 43 25.94 25.94 44 25.94 0.00 25 94 0.00 0.00 25.94 0.00 25.94 45 25.94 25.94 46 25._94 3 00 25.9* 9 00 25.94 0.00 25.94 0.00 25.94 47 25.94 46 25.94 0.00 25.94 0 00 25.94 0.00 25.94 49 25.94 0.00 0.00 25 94 50 25.94 0 00 25 94 25.94 0.00 25.94 51 25.94 0.00 0 00 25.94 52 25.94 0 00 25.94 25.94 0.00 25.94 53 25.94 0.00 CHLORINC MORTALITY: 6.255
~'i (a
1 a - - - ---- -- , - - - - - , , _ _ - . - - , , - - - - -
. l l
Salem 316(b) Demorstration d TABLE 6.1-16
SUMMARY
OF ENTRAINMENT MORTALITY: BLUEBACK HERRING EARLY JUVENILE OPERATION HISTORY: NO OUTAGE HIGH MORTALITY ESTIMATES
--.-------* E N T R AI N1C1T M OR T A LI TY (23-----------
m01 --.--0%IT 1----- ---- = U N I T 2----* JEK 74E9 MAL THE R 9 A L TOTAL THERMAL TOTAL 1 62 50 0.03 62.50 0.00 62.50 2 62 51 0.33 62.51 :.30 62 50 3 62.50 0.03 62.50 0.00 62.50 4 62 50 0.03 62 50 0.00 62.50 5 62.50 0.00 62.50 0.00 62.50 6 62 53 0 33 62.51 0.33 62 50 F 62.50 3.00 62.50 0.00 62.50 6 62 50 0.03 62 50 0.00 62.50 9 62.50 0.00 62.50 0.00 62.53 13 62.50 3 43 62.50 0 00 62.56 11 62.50 0.03 62.50 0.00 62.50 12 62.50 0.00 62.50 0.00 62.50 13 62 50 0.J3 62.55 0.00 62.50 14 62.50 0.00 62.50 0.00 62.50 15 62.50 0.00 62.50 0.00 62.50 16 62.50 0.00 62.50 0.00 62.50 17 62 50 0.01 62 50 0.JO 62.50 13 62.50 0.00 62 50 0.00 62.50 19 62.50 0.00 62 50 0.00 62 50 20 62.50 0.00 62.50 0.00 62.50 21 62 50 3.0) 62 50 0.02 62.51 22 62.50 0.02 62 51 0 14 62.55 frx 23 62.50 0.03 62.53 0.55 62 71
* \ 24 62.50 0.23 62.59 1.30 62 99 \~2 25 62 50 1.75 62.78 3.38 63 77 26 62 50 2 86 63.57 9.36 66.01 5 27 62.50 3.4T 63.80 11.25 66.72 29 62.53 9.51 65 69 22.08 70.78 29 62.50 21.31 70.49 42 23 78.33 30 62 50 19.27 69. 73 39.62 77.36 31 62.50 16.87 68.82 36.14 76.05 32 62 50 21.32 70 50 42 42 78.41 33 62.50 13.06 69.27 37.72 76.65 34 62.50 10 41 66.40 25.64 72 12 35 62 50 11. 70 66.89 27.96 72.98 36 62.50 7.61 65.35 20 16 70 06 37 62.50 1.62 63.11 6.16 64.81 38 62.50 0.49 62.68 2.30 63 36 39 62.50 0.05 62.52 0.38 62.64 40 62.50 0.01 62.50 0.05 62.52 41 62.50 0.00 62.50 0.00 62.50 42 62.50 0.03 62.50 0.00 62.50 43 62 50 3.J1 62 50 0 00 62 50 44 62 50 0.03 62.50 0.00 62.50 45 62 50 0.00 62 50 0.00 62.50 46 62.5C 0.03 62.50 0.00 62.50 47 62 53 0.0J 62 50 0 00 62.50 48 62.50 0.00 62.50 0.00 62.50 49 62.50 0.00 62 50 0 00 62.50 50 62.50 0.00 62.50 0.00 62.50 51 62 50 3.01 62.50 0.00 62.50 52 62.50 0.00 62.50 0.00 62.50 53 62.50 0.00 62.50 0 00 62.50 CHLORINE MORIALITY: 6.255
[o\ f
Salcm 316(b) Demonstration c3 TABLE 6.1-17
SUMMARY
OF ENTRAINMENT MORTALITY: ATLANTIC CROAKER JUVENILES
) OPERATION HISTORY: NO OUTAGE
........= ?NF4AIN9i1T M047ALITY (I)...........
NON
- ONI7 1 ..*- ...-. UNIT 2....-
J~.E4 f4C1 MAL TH711AL TOTAL TH(9 MAL TJTAL 1 40.00 0.03 40.00 0.00 40.00 2 40.00 0.0J 40.00 0 00 40.00 3 40 00 0.00 40.00 C. 0 0 40.00 4 43.1C J.D 41 00 0.no 4 0. Us 5 40.00 1.0J 40.00 0.00 40.00 6 40.00 0.00 40.00 0.00 40.00 7 40.00 3.00 40.00 0.00 40.00 9 40.3J A.01 43.00 0.00 40 0G 9 40.00 3.00 40.00 0.00 40.00 10 40.00 0.00 40.00 0.00 40.00 11 40 00 0.00 40.00 0 00 40.00 12 40 00 0.00 40.00 0.00 40.00 13 40.00 0.00 40.00 0.00 40.00 14 40.00 0.00 40.00 0.00 40.00 15 40.00 1 33 43 00 0 00 40.00 16 40.00 0.00 40.JO 0.00 40.00 17 40.00 0.00 40.00 0 00 40.C0 13 40.00 0.00 40.00 0.00 40.00 19 40 0J 3 01 40.00 0 00 40.DC 20 40.00 0.00 40.00 0.00 40.00 21 40.00 0 00 40.00 0.00 40.00 22 40.00 0.00 40.00 0 13 4 0. 0 A 23 40 30 3 31 40.JD 1.35 40.A1 /'~N 24 40.00 0.00 40.00 5.40 43.24 () 25 26 40 00 40.00 0.01 0.54 40 00 43.32 20.62 52.*77 52 37 71 66 P 27 40.00 0.51 40.31 64.99 79.00 28 40.00 4.57 42 74 39.43 93.66 29 40.00 2 9 . 14 57 24 99.01 99.40 30 40 40 23 89 54.34 98.86 99 32 31 40.00 19.63 51.18 98.20 ~,8. 9 2 32 40.00 23.53 57.15 99 20 99.52 33 40.00 21 51 52.91 98.24 98.94 34 40.00 6.94 44.17 92.26 95 96 15 40,00 9 81 45.29 95.10 97.06 36 40.00 3.73 42.27 8".11 91.06 37 40.00 0.08 40.05 39.26 63.56 18 40.00 0 13 43 03 12.72 47.63 39 40.00 0.00 40.00 0.74 40.44 to 40.00 0.00 40.00 0.02 40 01 41 40.00 0.J3 40.00 0 00 40.00 42 40.00 0.00 40.00 0.00 40.00 43 40.00 0.00 40.00 0.00 40.00 49 40 00 0.00 40.00 0.00 40.00 45 40.00 0 33 40 00 0.00 40.00 46 40.00 0.00 40.00 0.00 40.00 47 40.00 0.00 40 00 0.00 40.00 48 40 00 0.00 40 00 0 00 40 00 49 40 09 -) .1 J 40.00 0.00 40.00 50 40.00 0.00 40.00 0.00 40.00 51 40.00 0.00 40.00 0.00 40.00 52 40.00 3.00 40.00 0.00 40.00 53 40 00 0.J3 40 01 0.0f 40 00 CHLORINE MOR7ALI TY: 6.25% O L)
-- w
S513m 019)9( 02mousassajou )b m' 1VN'3 9 ' I- TF snHWYBA 03 3NIHVINH3NI WOHIVI'llA: SIHId3G GVSS 3DDS 0d3HY1 ION HISIOHA: NO 001V03
.-....---. 3N1brI sw3 h 1 hOdavll a A txt...-..-....
b0N . ..erh11 1..... .....ng11 E..... P}}) 1k3 bht 1 1H3hWT1 101Y1 1N3WMfi 101T1 1 9S*1E C*DC 9 6 ' IC O'00 9B* lC E 96*1E C'CC 9B*1( 0'00 9B* IC i 96*lF C*C( 9p*1( 0'00 90*TC 4 99*12 C*OC 9F*1f 0'00 9B*lC 5 99'lE 0'00 9k'it 0'00 9 8' 1C 9 9b*1E 0'00 9P*TE O'00 90* lC J SP*1E C*CC 9e*I( 0'00 99* Tt 9 99*1E 0*00 9E'it 0*00 99'IC t 9F*12 0'00 9E'ti O*00 98'1f 10 96'IE O'CC 98*1E O*00 SB* IC 11 96'IE O'DC 99*1( 0'00 98* 1C lE 9P*!E C*OC 9E*TE 0'00 99'IC lE 9e*1E C*rC 99'IC O'DC 9S* IC 16 9P*1E C*oC 98*11 O'00 96'IC 1G 99*1E 0'00 96*1( 0'00 9B* TC 19 99*1E 0'00 9 8* 1E 0'00 98* IC 11 99*1E C'CC 99*1( 0'00 9B* IC lE 99*1E C*OC 99'IE 0'00 99'IF 16 96'IE 0'00 99'it O'00 9B* 1C E0 9p*1E C*00 99'1C 0'00 98* 1C II 9e*1E C'CC 99'IE 0'CO 90* TC 22 9e'IE 0*DC 96 1( 0'00 99 it 99'IE 0'00 99*TC O'00 99'IC )_([ EC Eb 98*1E 0'00 99*1( O'00 99' tt ES 9f*1E C'CO 99'IC 0'C0 98' 1f p 29 9P*lE 0'00 96'IC O*00 98'IC EJ 96*12 0'00 96*17 C* OC 96'IC 36 99*1E C'CC 99'IC 0'CO 9B*TC 26 9E*1E 0*00 96'I( 0'00 98'1f fO 99*12 0*00 9 8
- 1C O'00 98' IC 11 96*1E C*00 99'1C 0'00 98'IC tE 9P*IE O'CC 98*1( 0'0C 98'IC ff 99'IZ 0'00 99 IC 0'00 99'IC 54 9S*!! 0'00 ? e 1C O*00 99' T E EG 99'IE C*00 9B*lf 0'00 9B* TT 19 99'IE C*CC 9F*lC 0'C0 98' i t tI 9B*1E 0*00 9S
- 1( 0'00 99' 1C t* 99'12 C*OC 96'IC 0'00 9 8' 1C f6 99*13 C*OC 99'it 0*00 9E* TC 6C 9E*1E C*OC 99'1( 0'00 9B*lC 61 99*1E 0'00 9b*1f 0'00 9B* IC tE 9P'IE 0'00 96'1C 0'00 98* TC 65 98*1E C*CC SB*IC 0'00 9k*lC 64 99*1E C*00 96*lC 0'00 9B' 1 C 6G 96'IE C*00 9B*lC O*00 9B* TC 69 9e*1E 0'00 9P'it O*00 99'!f 61 9S*IE C*0( 96*lC C*OC 9 b' IC 66 99'IE 0'00 yk*1C 0'00 99'IC 66 99'IE C*OC 99'TE 0*00 98* f f G0 98'1E 0*OC 99'IC 0'00 98' tt bl 96*13 0'00 9G*lC J'OU 96* TC 5E 99'IE C*00 98'1C 0*00 9S* tt G( 99 1E 0 00 98*tf 0 00 99* 10 3h10bik3 WCblr1111* 9* ESI J
- 4 N~/
Scicm 316(b) Demonstration g TABLE 6.1-19
SUMMARY
OF ENTRAINMENT MORTALITY: STRIPED BASS LARVAE OPERATIOtt HISTORY: NO OUTAGE
.. . .=. . * *Ei f 9 A !1 MENT MOR T A LI ====-UNIT TY ( E l --- . .2-*===
gom s. . *
- U N I T 1=====
TOTAL TPER*AL TOTAL dEEC THERMAL T4ERMAL 0.00 54.35 0.00 54.35 1 54 34 0.00 44.35 54639 0.00 54.35 2 J.3 0 54.35 0.03 54.35 3 54. 34 0.00 54.35 54.34 0.00 54.35 4 54.35 0.00 54.35 5 54.34 0.00 54.35 54.34 0.00 54.35 0.00 6 54.35 J.00 54.35 7 54.34 0.J 1 54.35 0.00 54.35 0.00 5 54.34 54.35 9 54.34 0.00 54.35 0 00 54.35 0.00 54.35 10 54.34 0.00 54.35 3.J4 54.35 0 00 11 54.34 0 00 54.35 54.34 0.00 54.35 12 54.35 0 00 54.35 13 54.34 0.00 0.30 54.35 0.00 54.35 14 54 34 54.35 54.34 0.00 54.35 0.00 15 54.35 0.00 54.35 16 54.34 0.00 54 34 0.00 54.35 0 00 54.35 17 54.35 0 01 54.?5 le 54.34 3 00 54.36 54.34 0.01 54.35 0 04 19 54.37 0 19 54.43 54.34 0 06 54.61 20 0.20 54.44 0 59 21 54. 34 1 37 54.97 54.34 0 52 54.58 22 54.84 2 64 55.55 23 54 34 1.08 56.13
- 1. T 0 55 12 3 91
; 24 54.34 6.15 57 15 54.34 2 86 55.65 25 56.69 10 09 58 95 26 54.34 5.14 59.54 5 87 53.02 11 37 4 27 54.34 16 75 61.99 54.34 9.29 58.59 23 61 50 15 80 66 12 29 54. 34 15 48 24.61 65.58 54.34 14.T T 61 09 30 60.58 23.06 64.87 31 54.34 13.65 25 87 66.15 54.34 15.70 61 51 32 60 92 23.77 65 20 -
33 54.34 14.18 18. 39 62.74 54.34 10.38 59.08 34 59.41 19.43 63 21 35 54.34 11 09 61 56 8 68 58.31 15 80 36 54.34 8 23 58.10 54.34 4.32 56 18 56.63 37 55 38 5.00 l 39 54.34 2.26 2 20 55 35 54.34 0 89 54.75 54.73 1 39 0 85 to 54.34 0.30 54.48 54.43 0 06 54.37 0 20 41 54. 34 0 04 54.36 54.34 0.01 54.35 42 54.35 0 01 54.35 l 43 54.34 0.00 54.35 0 30 54.35 J.01 44 54.34 0.00 54.35
- 54. 34 0.00 54.35 45 54.35 0.00 54.35 46 54.34 0.00 54.35 0.00 54.35 0.00 j 47 54.34 54.35 0.00 54.35 4a 54.34 0 03 0.00 54.35 54.34 0.00 54.35 49 54.35 0 00 54.35 50 54.34 0.00 54.35 0.00 54.35 0 00
( 51 54.34 54.35 0 00 54 35 I 52 54.34 0 00 0.00 54.35 54.34 0.00 54.35 j 53 CHLO41NE MORTALITY: . 253
/
s c
)
Salen 316(b) Damonstretion p TABLE 6.1--20
SUMMARY
OF ENTRAINMENT MORTALITY: WHITE PERCH PROLARVAE OPERATION HISTORY: NO OUTAGE V
..*** ..= = .=CNT94 I1MC1T MOR T ALI TY (18-======....
MON .>..= UNIT 1.=*.< . ..=U1tf 2=.=== JICC THERMAL T4ER1AL TOTAL THf4 MAL TOTAL 1 54.06 0.03 54 06 0.00 54 06 2 54.06 0.00 54.06 0.00 54.06 3 54.*4 1. J J 54.06 0 31 54.06 4 54 06 0.30 54.06 0.00 54.06 5 54.06 0.00 54.06 0.00 54.06 6 54.06 0.30 54 06 0.00 54.06 7 54 06 J.J? 54.06 .30 Sa.06 9 54.06 0.30 54.06 0.00 54.06 9 54.06 0.00 54.06 0.00 54.06 10 54.06 0.00 54.06 0.00 54.06 11 54.06 J.33 54.16 u.00 54.06 12 54.06. 0.00 54.06 0.00 54.06 13 54.06 0.00 54.06 0.00 54.06 14 54 06 0 30 54.06 0.30 54 06 15 54.06 0.00 59.06 0.00 54.06 16 54.06 0.00 54.06 0.00 54 06 17 54.06 0.00 54.06 0.00 54.06 18 54.36 0 33 54.36 0 00 54.06 19 54.06 0.30 54.06 0.00 54.06 23 54 06 0 00 54.06 0.00 54.06 21 54.06 0.30 54.06 0.00 54 06 22 54 06 J.31 54.06 O s01 54.07 23 54.06 0.00 54.06 0.03 54.07 fg 24 54.06 0.00 54.06 0.08 54 10 > i 25 59.06 0.32 54.07 0.26 54 18 \/ 26 54.06 0.11 54.11 1.12 54.58 27 59.06 0 12 54.12 1 35 54.68 29 54.06 3.46 54 27 3.69 55.75 29 54.06 1 79 54.95 10.69 $8.97 30 54.06 1 65 54.92 9.43 59.40 31 59.06 1 32 54.67 d.06 57.76 32 54.06 1.95 54.96 10.65 58.95 33 54.06 1 51 54.75 8.77 59.09 34 54.06 0.62 54.35 4.61 56.18 35 54.06 0.14 54.40 5.27 56.49 36 54.06 0.40 54 25 3 26 55.56 17 54.06 0.04 54.08 3.59 54.34 34 54.06 0.31 54.0 7 0 16 54 14 31 54.06 0.J O 54.06 0.02 54.07 41 54.36 J.30 54.06 2.0c 54.06 41 54.06 0.30 54.06 0.00 54.06 42 54 06 0.30 54 06 0.00 54.06 43 54.06 0.00 54.06 0.00 54.06 44 54.06 1.30 34.06 0.30 54.06 45 54.06 0.30 54.06 0.00 54.06 46 54.06 0.J O 54.06 0.03 54.06 tr 54.06 0.30 54.06 0.00 54.:6 49 54.06 0 33 54.06 0.00 54.06 49 54.06 0.30 54.06 0.00 54.06 50 54.06 0.00 54.06 3.00 54.06 51 54.06 0.00 54.06 1.3* $4.C6 52 54.06 0.JO 54.05 0.00 54.06 53 54.06 0.30 54.06 0.00 54.06
..... ..........................................=.......
C1 Lot !1C 10R T ALI T f : 6.251 {~%
m Salca 316(b) D:monstrction O V TABLE 6.1-21
SUMMARY
OF ENTRAINMENT MORTALITY: WHITE PERCH POSTLARVAE OPERATION HISTORY: NO OUTAGE
-..= =.-=.-
- E4 f 44144CN T M04 f a LI f f (33...........
NON *=**.U11T 1.==.* ***.* UNIT 2*...* d!C( THERMAL tie 114L TOTAL T H{ t N A L 73 f a L 1 29.69 0.30 29.69 0.00 29.69 2 29.69 3.J 4 29.69 0.00 29.69 1 29.69 0.30 29.69 0.00 29.69 4 29.69 0.00 29.69 0 00 29.09 5 29.69 0.00 29.69 0.00 29.69 6 29.69 31.2 29.69 0.00 29.69 7 29.69 0.30 29.69 0.00 29.69 9 29.69 0.00 29.69 0 00 29.69 9 29. 69 0.00 29.69 0.00 29.69 13 29.49 0.30 29.69 0.00 29.69 11 29 69 0.30 29.69 0.00 29 69 12 29.69 0.30 29.69 0 00 29.69 13 29.69 3.J D 29 69 0.00 29.69 14 29.69 0.30 29.69 0.00 29.69 15 29.67 0 30 29.69 0.00 29.69 16 29.69 0.31 29.69 0.02 29.70 17 29.69 3.35 29.72 0.09 29.75 18 29 69 0.14 29,79 0.25 29.86 19 29.69 0.39 29.96 0.65 30 14 20 29.69 1.39 30.66 2.14 31 19 21 29.69 3. 3 a 32.07 4.94 33.16 [~') 22 29 69 6 31 34.13 8.78 35.46 \s,/ 23 29.69 10.38 36.98 13.91 39.47 24 29.69 13.35 39.43 18 12 42 43 25 29.69 19.12 43.13 24.28 46.76 26 29.69 26.79 48.52 32.82 52 76 27 29 69 29.33 50.29 35.62 54.73 29 29.69 37.95 56.37 44.79 61.18 29 29.69 50.3 3 64.86 57.00 69.77 30 29.69 48.63 63.88 55.64 69.81 31 29.69 46.64 52 51 53.70 67.45 32 29.69 50.1 7 54.96 57 15 69.87 33 29.69 47.52 63.10 "4.52 68.02 34 29.69 40.36 58.36 47 29 62.94 35 29.69 +1.S5 59.11 48.82 64.01 36 29.69 36.42 55.30 43.17 60.04 37 21.69 23.42 46 16 29 14 50.1R 39 29.69 16.43 41 24 21 14 44.55 39 29.69 9.36 36.3b 12.27 39.32 40 29.69 4.39 32.78 6.27 34.10 41 29.69 1.41 33 64 2 17 31 22 42 29.69 0.3d 29.96 0.64 30.14 43 29.69 0.16 29.40 0.29 29.88 44 29.69 3.34 29.75 0.15 29.19 45 29.6+ 31+ 29.71 e .0 F 29.73 46 29.69 0.31 29.69 0.02 29.70 47 29.69 0.30 25.69 0.00 29.69 48 29.69 0.30 29 69 0.00 29.69 49 29.69 2 31 29 69 J . 3 -3 29 69 53 29.64 0.30 29.69 0.00 29.69 51 29 .69 0 31 29.69 0.00 29.69 52 29.69 J.3 0 29.69 1.30 29.69 53 29.44 . .) # 29.69 .00 29.69 CHLO111C 90974Liff: 6.253 (
/
Q
Salsa 316(b) Dimonstration O V TABLE 6.1-22
SUMMARY
0F ENTRAINMENT MORTALITY: BAY ANCHOVY JUVENILES AND ADULTS OPERATION HISTORY: NO OUTAGE
. 4........ENT41111C9f MOtf4LIff (54...........
N T4 ..*** UNIT 1..... .**.. UNIT 2...
- WEE ( T1544aL fatagaL TOTAL TMregat forat 1 ile t ? 3 30 9T.19 0.30 9F.19 2 97.19 0.30 97.19 0.00 97.19 3 97 19 0 00 17.19 0 00 9F.19 4 97 19 0.30 9T.19 0.00 97.19 5 97 19 0.30 97 19 0.00 9T.19 6 97.19 0.33 97.19 0.00 97 19 F 97 19 0.00 97 19 0.00 97.19 9 97 19 0.00 97 19 0.01 97.19 4 97.19 0.30 97 19 0.00 97.19 13 97.19 0.30 97.19 0.00 97.1?
11 97 19 0.30 97.19 0.00 97.19 12 97 19 0.30 17 19 0.00 97 19 13 97 19 0.30 97.19 0.00 97 19 14 9 F.19 0.00 97 19 0.00 97.19 15 97.19 0.00 97 19 G.00 97 19
. 16 97.19 J.3 0 9T.19 0.0J 97.19 17 97 19 0.00 97 19 0.00 97.19 il 9F.19 0.00 97.19 0.01 97.19 19 97 19 3.)J 97 19 0.05 97 19
./'S 23 97.19 4.02 97.19 0.23 97.19 i 21 97.19 0.06 97 19 0.72 97.21 t
22 97 19 0.18 97.19 1.64 97.23 21 97 19 3 41 97 2S 3 14 97.28 24 97.19 0.59 97.21 4.62 97.32 25 97.19 1.24 97.22 7 18 97 39 26 97 19 2 46 97.26 11 62 97.51 27 9 T.19 2 95 97.2T 13.0F 9T.56 24 97 19 4.97 97 32 19.01 97.72 29 97 19 9.04 97.44 28.80 98.00 30 97 19 8.41 97.42 27.53 97 96 31 97.19 7.65 97.40 25.87 97.91 32 97 19 9.04 97.44 28.88 98.00 33 97.19 8.32 97.41 26.62 97.94 34 97 19 5.54 97.34 21 80 97.77 35 97.19 5.99 97,36 21.94 9r.90 36 97 19 4.51 97 31 17.16 97.69 37 97.19 1 85 97.24 9.55 97.46 l 38 97 19 0.96 97 21 5.87 9T.35 39 97.19 0.33 97.20 2.63 97.26 40 97 19 0 10 97 19 1 02 97 22 41 97 19 3 32 97 19 0 24 97.19 42 97.19 0.30 97.19 0.05 97 19 43 97 19 0.00 97.19 0.02 97 19 44 9 F.19 0.00 97 19 0.01 07.19 45 97 19 0.30 97.19 0.00 97.19 46 97.19 0.30 97.19 0.00 97.19 4F 97.19 0.30 97.19 0.00 97.19 49 97 19 0.00 97 19 0.00 97.19 l 49 97 19 0.00 97.19 0.00 97 19 I 50 97.19 0.30 97.19 0.00 97.19 i 51 97 19 0.30 97 19 0.00 97 19 52 97.19 0.00 97 19 0.00 97 19 53 17 19 0.30 97.19 0.00 97 19 CHL1 TINE 4CATALITY1 6.235
(}
Salem 316(b) Dtmonstration O V TABLE 6.1-23
SUMMARY
OF ENTRAINMENT MORTALITY: WEAKFISH PROLARVAE AND POSTLARVAE OPERATION HISTORY: NO OUTAGE
.**. . .. .
- a . C1 f t a !11C 1 T 40tTALIf7 (43-..........
411 ....* UNIT 1. . . . a .a.*.UN17 2.... WEE ( THC91AL 71C41 AL TOTAL TH!tM4L TOTAL 1 43.75 3.30 43.75 0.00 43.75 2 43 75 0.J O 43.75 0.00 43 75 3 43. 75 0.33 43.15 0 00 43.75 4 43. 75 13? 43 15 ?.3* 43.75 5 43.75 0.30 43.75 0.00 43.75 s 43. 75 0.30 43.75 0.00 43.75 7 43. 75 0 30 43.75 3.00 43.75 3 43. 75 3 39 43.75 1 0e 43.75 9 43. 75 0.00 43.75 0.00 43.75 10 43 75 0. J 0 43 75 0.00 43.75 11 43.75 0.30 43.75 0.00 43.75 12 43.F5 0.30 43.75 0. 00 43.75 13 43.75 0.00 43.75 0 00 43.75 14 43.75 0.00 43.75 0.00 43.75 15 43.75 J.30 43.75 3.00 43.75 16 43.75 0.30 43.75 0.00 43.75 17 43.75 0.00 43.75 0 00 43 75 19 43.75 0.30 43.75 0.02 43.76 19 43 75 3.31 43 75 3 12 43.82 20 43. F5 0.
- J 43.79 0.75 44 17 f-'3 21 43.75 0.37 43.96 2 69 45 26 22
(' ') 23 43.75 43.75 1 22 2 98 84.43 45.37 6.48 12.42 47.40 50.74 24 43.75 4.30 46.45 17.94 53.84 25 4 3. 75 3.50 48.53 26 57 58.69 26 43 75 15.3* 52 47 38.89 65.62 27 43.75 17.30 53.75 42.97 67.92 24 43 75 27.43 59 21 55.35 75.17 24 43. 75 42.13 67.90 11 41 83.92 33 43 75 41 33 66.R3 69.86 83.35 31 43.75 38.45 55.39 67.49 81.71 32 43 75 43.09 67.99 71.66 84 06 33 4 3. 75 34 60 66.02 68.45 92 25 34 43 75 34.39 63 94 '9 23 77.07 35 43. 75 32.23 51.39 61 .27 79.22 36 43.75 2 5. F F 58.25 53 58 T3.A9 37 4 3. 75 12.16 50.59 33.59 62.64 39 43. 75 s. s 3 47.45 22.17 55.22 37 43. 75 2. 2 % 45.33 10.44 49.62 to 43.75 0.63 44.11 3.95 45.9F 41 43.75 ..J d 43.93 3.71 44 19 42 43. 75 0.31 43.75 0.11 43.81 ! 43 43. 75 0.30 43.75 3.03 4 3. F 7 44 43.75 0.00 43.F5 0.31 43.76 45 43 75 ;.J7 43.75 7.1' 43.75 46 43. 75 3.JG 43.15 0.01 43.F5 4F 43.75 J.3 0 43.75 0.00 43.75 49 43. 75 0.00 43.75 0.00 43.75 41 43. F5 s.39 43 75 G.4) 43.15 50 4 3. 75 0.33 43.75 3.00 43.75 51 4 3. 75 0.39 *3.75 3.00 +3.75 52 43.15 3. J 3 4 3. F 5 0.00 43.75 l 51 43.75 0.30 43.75 1.10 43.75 l i 4L34:NE M19Fic;ff: 6.25 s 7-~g Ys , l
,e- - - ---
w m w w e -,c --
Salem 316(b) Dtmonstration (dD TABLE 6.1-2L
SUMMARY
OF ENTRAINMENT MORTALITY: WEAKFISH JUVENILES OPERATION HISTORY: NO OUTAGE
.***.a..e +51T34!1%CNT MORTALITY (t)=====.-==*=
NON == = = = UN I T 1.*=.* *==** UNIT 2=*=.= JEE( T4C4 MAL fiC81 AJ Total T HE 4.9 AL T374L 1 53.13 0.J 0 53 13 0.00 53.13 2 53 13 3 33 53 13 0 00 53 13 3 53.13 3.10 53.13 0.00 53.13 4 53.13- 0 00 53.13 0.00 53.13
,5 53.13 0.00 53.13 0.00 53.13 5 53.13 3 30 53 13 0.00 51.13 7 53.13 0.30 53.13 0.00 53.13 9 53. 13 0.30 53.13 0.00 53.13 9 53.13 0 00 53.13 0.00 53.13 13 53 13 0.30 53.13 0.00 53.13 11 53.13 0.00 53.13 0.00 53.13 12 53.13 0.00 53.13 0.00 53 13 13 53.13 0 00 53 13 0.00 53.13 14 53.13 0.00 53 13 3 30 53 13 15 53.13 0.30 53.13 0.00 53.13 16 53.13 0.00 33 13 0.00 53 13 17 53.13 0.00 53.13 0 00 53.13 13 53 13 3 33 53 13 1 02 53.14 19 33.13 0.31 53 13 0.12 53.18 20 53 13 0.08 53.16 0.75 53.48 21 53.13 0.37 53.30 2.69 54.39 22 53 13 1.22 53.70 6.49 56.16 23 53.13 2.38 54.47 12.42 53.95 gg 17.99 61.54
! 1 24 - 53.13 4.30 55 38
\- ' 25 53 13 8.50 57.11 26.57 65.58 26 53.13 15.50 50.39 3a.88 71.35 27 53 13 17.30 61 47 42.97 73.2 7 29 53.13 2 F.4 8 66.01 55.85 19.31 29 53.13 42 33 73 25 71 41 96.60 33 53 13 41.33 T2.36 69.36 95.97 31 53.13 38.45 71.15 67.49 84.76 32 53.13 43.09 73.32 71.66 86.71 33 53 13 39.6J 71 69 68 45 85.21 34 53.13 30.39 57.37 59.23 80.39 35 53.13 32.2 3 64 23 61 2F 81.85 36 53.13 25 77 55.20 53.58 78.24 37 53.13 12.16 58.83 33.59 69.87 33 53.13 6.50 56.22 22.17 63.52 31 53 13 2. 2 d 54.19 10.44 53.02 43 53.13 ?.6 3 53.42 3.95 54.97 41 53.13 0.38 53.16 0.79 53.50 42 53.13 0.31 53.13 0.11 53.18 s 43 53.13 0. J 0 53.13 0.33 53.14 44 53 13 3.J3 53 13 G.01 53 13 45 33.13 0.30 53.13 J.00 53.13 46 53.13 0.00 53.13 0.00 53.13 4F 53.13 0. 3 J 53.13 0.00 53.13 44 33 13 0.30 53.13 0.00 51.13 44 53.13 0.30 53.13 0.00 53.13 50 53.13 0.00 53.13 0.00 53.13 il 53.13 0.00 53.13 2 07 53 13 32 53.13 3.30 53.13 0.03 53.13 53 53.13 0.30 53.13 3 00 53.13 C4LO114C 90if4LITY1 4.253 O
- V
Salee 316(b) Demonstration O TABLE 6.1-25
SUMMARY
OF ENTRAINMENT MORTALITY: Neomysis americana OPERATION HISTORY: NO OUTAGE
. .....=**.* E 47 A 4! 1ME 17 M OR T A LI T7 (18*.-====..==
NON === ==U 117 1===== ===== UNIT 2-==== JCEN THCRMAL THE RMA L TOTAL THERMAL TOTAL 1 11.51 0.00 11.51 3.00 11 51 2 11.51 0.00 11.51 0.00 11.51 3 11.51 0.00 11.51 0.00 11.51 4 11 51 0.00 11 51 0 00 11.51 5 11 51 0.00 11 51 0.00 11 51 6 11.51 3.03 11 51 0 00 11 51 7 11.51 0.00 11.51 0.00 11 51 8 11.51 0.00 11 51 0.00 11 51 9 11 51 3.03 11.51 0.00 11.51 13 11 51 J.00 11 51 0 00 11 51 11 11.51 0.00 11 51 0.00 11 51 12 11.51 0 00 11.51 0.00 11 51 13 11 51 3.03 11 51 0 00 11 51 14 11.51 0.00 11.51 0.00 11 51 15 11.51 0.00 11 51 0 00 11 51 16 11.51 0.00 11 51 0.00 11 51 17 11.51 3 30 11 51 0.33 11 54 18 11.51 0.01 11.52 0.15 11.64 19 11.51 0.07 11.57 0.63 12 07 20 11.51 0.52 11.97 3 27 14.40 21 11.51 2.11 ~ 13.38 9.56 19.97 ((,")/ 22 11.51 5.55 16.42 18.93 28 26 23 11.51 11.22 21.44 31 14 39.07 24 11 51 16.71 26.29 40.98 47.33 25 11.51 25 .52 34.09 52.65 58 10 26 11.51 38.38 45.48 66.09 69.99 27 11.51 42 67 49 27 70 52 73 91 23 11.51 56. 25 61.24 81 08 83 26 29 11.51 72 51 75.68 90.65 91.73 30 11.51 73 91 74.26 89 90 91 07 31 11.51 68 .45 72.08 88.60 89.92 32 11.51 72.77 75.91 90.84 91 89 33 11.51 69.44 72 96 89.07 90.33 34 11.51 59.80 64.43 83 48 85 38 i 84.85 86.60 35 11.51 61. 95 6 6. 33 l 81.61 36 11.51 53.86 59.17 79.22 37 11.51 32.83 40.56 60.89 65. 39 38 11 51 21.32 33 11 46.47 52 63 39 11.51 9.29 19.73 27 30 35 67 40 11.51 3.23 14.37 12 82 22.85 41 11.51 3 . 56 12.00 3.37 14 50 42 11.51 0.06 11.57 0.61 12.05 43 11.51 0.01 11.52 0 17 11.66 44 11.51 0.00 11.51 0.07 11.57
.5 11 51 3.03 11 51 ~ 0 02 11 53 46 11.51 0.00 11.51 0.00 11.51 l 47 11.51 0.00 11.51 0.00 11 51 i
48 11.51 0.00 11.51 0 00 11 51 49 11.51 0.00 11.51 0.00 11.51 50 11 51 0.00 11 51 0 00 11 51 51 11.51 0.00 11.51 0.00 11 51 52 11 51 3 00 11 51 0 30 11 51 53 11 51 0.00 11.51 0.00 11.51
,,- s CHLORINE 80RTALIt71 0. 0 I
Salem 316(b) Demonstration ( V TABLE 6.1-26
SUMMARY
OF ENTRAINMENT MORTALITY: Gammarus sp. OPERATION HISTORY: NO OUTAGE
-----------E9T9tI1951T notTt . ITf ts -----------
NON -- --- UN I T 1 ----- - -- --UN I T 2 -- -- - dEEC fME9 MAL THC9 4 AL TO7AL T HC 4 M AL 70fAL 1 4.95 0.00 4.95 0.00 4.75 2 4.95 0.00 4.95 0.00 4.95 3 4.95 0.00 4.95 0.00 4.95 4 4.25 0 00 4.45 0.00 4.95 5 4.95 0.00 4.15 0.00 4.55 6 4.95 0.00 4.95 0.00 4.95 7 4.95 0.00 4.95 0.00 4.95 3 4.95 0.00 4.95 0.00 4.95 9 4.95 0.00 4.95 0.00 4.15 10 4.95 0.00 4.95 0 00 4.95 11 4.95 0.00 4.95 0 00 4.95 12 4.95 0.00 4.95 0.00 4.95 13 4.?S 0.00 4.95 0.00 4.95 14 4.95 0.00 4.95 0.00 4.95 15 4.95 0.00 4.?5 0 00 9.95 16 4.95 0.00 4.95 0.00 9.95 17 4.95 0.00 4.95 0.00 4.95 19 4.95 0.00 4.95 0.00 4.95 19 4.95 0.00 4.95 0 00 9.95 20 4.95 0.00 9.95 0.00 4.95 21 4.95 0.00 4.95 0.02 4.97 22 4.95 0.00 4.95 0.10 5.04 [~ 'T 23 4.95 0.01 4.95 0.28 5.21 (~s/ 24 4.95 0.01 4.86 0.54 5.46 25 4 15 0.04 4.98 1 15 6.04 26 4.95 0.14 S.08 2.74 7.55 27 4.95 0.17 5.10 3.23 1.02 29 4.95 0.43 5.36 6.18 10.82 29 4.95 1.31 6.19 12.70 17.02 30 9.95 1 13 6.02 11.69 16.06 31 4.95 0.96 5.36 10.49 14.92 32 4.95 1 29 6.18 12.71 17.02 33 4.95 1 05 5.95 11 .08 15.48 34 4.95 0.54 5 46 7.20 11 79 35 4.15 0.62 5.53 7 84 12.44 l 36 4.95 0.38 5.31 5.65 10.32 l 37 4.95 0.08 5.02 1.90 6.75 38 4.15 0.03 4.97 0.83 5.74 l 39 4.95 0.00 4.95 0.21 5.15 40 4.95 0.00 4.95 0.04 4.99 41 4.25 0.00 4.95 0.00 4.95 42 4.45 0.00 4.95 0.00 9.95 43 4.95 0.00 4.55 0.00 4.95 44 4.95 0.00 4.95 0.00 4.95 45 4.*5 0.00 9.95 0.00 4.95 46 4.95 0.00 4.*5 0.00 4.95 i 4.95 47 4.*5 0.00 4.95 0.00 l 48 4.95 0.00 4.95 0.00 4.95 l 49 4.95 0 00 4.95 0.00 ' 95 50 4.95 0.00 4.95 0.00 4.95 51 4.95 0.00 4.95 0.00 4.95 52 4.95 0.00 4.95 0.00 4.95 53 4.95 0.00 4.*5 0.00 4.95 OHL;t114 439TALITY: 3.62E G
' ,/ Y .
l
Salem 316(b) Demor.stration m,. I n LJ TABLE 6.1-27 PROJECTED NUMBER OF CWS PUMPS OPERATING EACH WEEK AT SALEM UNITS NO. 1 AND NO. 2 UNDER VARIOUS OUTAGE SCHEDULE FOR 100 PERCENT POWER AND PUMPING EXCEPT DURING REFUELING No Outate Sprima Outate Fall Outage combined outsee Unit unit Unit ca st Unit Unit Calendar unit untt No. 2 Me. 2 Week No.1 No. 2 Me. I Mo. 2 Me. t No. t 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 4 6.0 4.0 6.0 6.0 6.0 6.0 6.0 2 6.0 6.0 9.0 3 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0
= 6.0 6.0 6.0 5 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6 6.0 6.0 6.0 7 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 8 6.0 6.0 6.0 9 6.0 6.0 6.0 6.0 5.0 6.0 5.6 6.0 6.0 6.0 6.0 5.4 10 6.0 6.0 6.0 8.6 11 ~ 6.0 6.0 L.6 6.0 6.0 6.0 6.0 1.0 6.0 6.0 6.0 6.0 1.0 12 6.0 1.0 13 6.0 6.0 1.0 6.0 6.0 6.0 6.0 1.0 6.0 6. 0 6.0 6.0 1.0 14 6.0 6.0 1.0 6.0 6.0 1.0 6.0 6.0 6.0 6.0 15 1.0 6.0 1.0 6.0 6.0 6.0 6.0 16 6.0 1.0 17 6.0 6.0 1.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 1.0 18 6.0 6.0 1.0 6.0 6.0 1,0 6.0 6.0 6.0 6.0 1.0 19 6.0 0.0 1.0 20 6.0 6.0 1.0 6.0 6.0 6.0 6.0 1.6 6.0 6.0 6.0 6.0 i.6 21 6.0 6.0 5.6 6.0 6.0 1.4 6.0 6.0 6.0
/9 22 23 6.0 6.0 6.0 6.0 6.0 6.0 6.0 4.0 6.0 6.0
*I *J 24 4.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 25 6.0 6.0 6.0 6.0 26 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 s.0 27 6.0 %.0 28 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 29 6.0 30 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 31 6.0 - t.0 6.0 6.0 32 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 33 6.0 6.0 e.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 3t. 6.0 6.0 35 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0
. 34 6.0 4.0 6.0
.37 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 0.0 4.0 38 6.0 6.0 e.0 6.0 6.0 6.0 6.0 5.7 5.7 6.0 39 6.0 6.0 6.0 6.0 6.0 6.0 2.0 2.0 6.0 40 6.0 1.0 6.0 6.0 . 6.0 6.0 6.0 6.0 1.0 41 1.0 *.0 6.0 6.0 60 6.0 6.0 1.0 42 1.0 6.0 6.0 6. 0 , 6.0 6.0 6.0 1.0 43 1.0 6.0 44 6.0 6.0 6.0 6.0 6.0 1.0 6.0 6.0 6.0 1.0 1.0 6.0 45 6.0 6.0 6.0 6.0 4.0 6.0 1.0 1.0 4.0 46 6.0 1.0 %.0 47 6.0 6.0 6.0 6.0 6.0 1.0 6.0 6.0 1.0 f.0 6.0 48 6.0 6.0 6.0 6.0 6.0 6.0 6.0 1.0 1.0 6.0 49 6.0 1.3 a.0 50 6.0 6.0 4.0 6.0 6.0 1.3 6.0 6.0 6.0 5.0 5.0 4.0 51 6.0 6.0 6.0 6.0 6.0 6.0 6.0 4.0 n.0 52 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 6.0 53 la) Note that the combined outage schedeste for Unit Mos. I and 2 it reversed from the spring sad f att outages.
J
,5 n 4
[ v i l r h
- - ~ -
,g e , .-. m . , .- -. . , . - a ,v-, , , -
Salem 316(b) Demonstration f% e 5 ) V l TABLE 6.1-28 PROJECTED NUMBER OF CWS PUMPS OPERATING EACH WEEK AT SALEM UNITS NO. 1 AND NO. 2 UNDER VARIOUS OUTAGE SCHEDULE FOR TYPICAL FULL POWER OPERATION ps Outare Sprint Outane Fett Outate Cembined Nt ae+ Calendar Unic Unit 1:nic Unit Unit Unit unic Unic Week No. I No. 2 No. I po. 2 wo. I No. 2 No. I No. ' t 1. 3 ' 5.0 5.3 5.0 5.3 5.0 5.3 5.? 2 5.3 5.0 5.1 5.0 5.1 5.0 5.3 5.0 3 5.3 5.0 5.3 5.0 5.3 3.0 5.3 9.0 4 5.3 5.0 3.3 5.0 1.3 3.0 5.3 5.0
-5 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.0 6 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.0 7 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.0 6 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.0 9 5.3 5.0 5.3 5.0 5.3 5.0 5.3 1.0 to 5.3 5.0 a.8 5.0 5.3 5.0 3.3 a.5 Il 5.3 5.0 1.5 5.0 5.3 5.0 5.3 1.5 12 1.3 5.0 1.0 5.0 5.3 5.0 5.3 L.0 13 5.3 5.0 1.0 5.0 5.3 5.0 5.3 1.0 14 5.3 5.0 1.0 5.0 5.3 1.0 5.3 1.0 15 5.3- 5.0 1.0 5.0 5.3 5.0 5.3 1.0 16 5.3 5.0 1.0 5.0 5.3 5.0 5.3 t.0 17 5.3 5.0 1.0 5.0 5.3 3.0 5.3 1.0 15 5.3 5.0 1.0 5.0 5, 3 5.0 5.3 1.0 19 5.3 5.0 1.0 5.0 5.3- 5.0 5.3 1.0 20 5.3 3.0 1.0 5.0 5.3 5.0 5.3 1.0 2t 5.3 5.0 1.5 5.0 5.3 5.0 3.3 1.5 22 5.3 5.0 4.8 5.0 5.3 5.0 5.3 4.5 23 5.3 5.0 5.3 5.0 5.3 5.c 5.3 5.0 (O f 24 25 5.3 5.3 1.3 5.0 5.0 5.0 5.3 5.3 5.3 5.0 5.0 5.0 5.3 5.3 5.0 5.0 5.3 5.3 5.0 5.0 26 5.3 5.0 5.3 5.0 27 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.3 28 5.3 5.0 5.3 5.0 5.3 5.0 5.3 1.0 29 1.1 3.0 5.3 5.0 5.3 1.0 5.3 5.0 30 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.0 31 5.3 5.0 5.3 3.0 5.3 5.0 5.3 3.0 32 5.3 3.0 5.3 5.0 5.3 5.0 5.3 5.0 33 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.0 34 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5A 35 5.3 5.6 5.3 5.0 5.3 5.0 5.3 53 36 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.n 37 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.n 39 5.3 5.0 5.3 5.0 5.3 5.0 5.3 5.n 39 5.3 1.0 3.3 5.0 5. 3 - 6.8 5.0 5.0 40 5.3 5.0 5.3 5.0 5.3 t.s !.* 5.0 41 5.3 5.0 5.3 5.0 5.3 1.0 1.0 5.0 42 5.3 5.0 1.3 3.0 5.3 t.0 1.0 5.0 43 5.3 5.0 5.3 5.0 5.3 L.0 1.0 5.0 64 5.3 5.0 . 5. 3 5.0 1.3 1.0 1.0 1.0 45 5.3 5.0 5.3 5.0 5.3 1.0 1.0 5.0 46 5.3 5.0 5.3 5.0 5.3 . t.0 1.0 5.0 47- 5.1 5.0 5.3 5.0 5.3 1.0 1.0 5.n 68 5.3 5.0 - 5.3 5.0 5.3 1.0 1.0 5.0 49 5.3 5.0 5.3 5.0 5.3 1.0 1.0 5.0 50 5.3 5.0 5.3 5.0 5.3 1.2 1.3 5.0 3L 5.3 5.0 5.3 5.0 53 4.2 4.4 5.0 52 5.3 5.0 5.3 5.0 5.3 5.0 1.3 5.0 53 5.3 5.0 3.3 5.0 5.3 5.0 5.3 3.0 (a) Note that the Combined outage schedule for Unit Mos. I and 2 is reversed frose the spring and felt outages.
/ \
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s Salem 316(b) Drmonstration (Gl
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_c _ NO OUTAGE - HIGH MORTALITY ESTIMATE- ~ 4 UNIT 2- UNiiS 9 4 2.
....................... UNIT 4 MEAN ENIR . MORTAttiv SWS CWS TOTAL MORTALITV SWS CWS TOIAL COMBINED
$ RATE NUMBER NUMBER NUMBER TOTAL. WEEN. DENSITIES . RATE -NUMBER NUM8ER- NUMnER 4 0,0 0.625 0,0 0.0 0,0 0.625 0.0 0.0 0.0 0.0 5 0.0 0.625 0.0 0.0 0.625 0.0 0.0 0.0 0.0 j 2 . 0. 0 0.0 0.0, 3 ' 0,0 0.625 0.0 0.0 0.0 0,625 0.0 0.0 j 0.0 0.0 0.0 0.0 4 O0- 0.625 0.0 0.0 0.0 0.625 4 5 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0
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0.0 0.0 0.625 'O.0 0.0 I 0.0 0.0-t- 6 0.0 0.625 0.0 0.0 0.0 4 7 0.0 0.625 0. 0 - 0.0 0.0 0.625 0.0 0.0 8 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 j 9 0.0 0.625 0.0 v.0 0.0' O.625 0.0 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 y, 1 . to 0.0 0.625 0.0 0.0 0.0 0.0 O.0 0.0 y et . 0,0 0.625 0.0 0.0 0.0 0.625 0. 0 ' 0.0 0.625 0.0 0.0 0.0 0,625 :0,0 0.0 0.0 0.0 p. 12 0.0 e 13 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0
$4 - 0.0 0.625 0.0 0,0 0.0 0.625 0.0 0.0 0.0 0.0 9 45 - 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 68 16 0.0 0.625 0.0 0.0 0.0 0.625 '
SF 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 C"h i O.0 0.0 i le 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0' i 19 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 . 0.0 0.0 ([ , 20 0.07 0.625 2.8450D*03 4.53820*04 4.8227D*04 0.625 2.8450D*03 4.53820*04 4.82270804 9.64530*O se ]' 0.625. 8.53490603 9.3615D*05 9.44690805 2.8937D80 29 0.59 0.625 8.5349D*03 0.3604D*05 9.44680'05 0.0 22 . 0.0 0.625 0.0 0.0 0.0 0.626 0.0 0.0 0.0 C2 0.627 4.9915D*03 3.9872D*04 3.38630*04 6.7637D*0 4 23 0.82 0.625 0.9995D*03 3.8782D*04 3 3774D*04 4.6009D'O B 24 0.08 0.626 1.3504D*03 2.8585D*04 2.2937D*04 0.630 9.3584D003 2.1729D604 2.3072D*04 O 25 0,02 0,628 3.5562D*02-5.6903D*03 6.04590*03 0.638' 3.5562D*02 5.7584D003 6.88400'03 1.2860D*O 26 0.0 0.636 0.0 0.0 0.0 0.660 0.0 0.0 0.0 0.0 0.0 0.0 , 27 - 0.0 0.638 0.0 0.0 0.0 0.667 0.0 0.0 rt 28 0.0 0.657 0.0 0.0 0.0 0.708 0.0 0.0 0.0 0.0 y 4 29 0.0 0.705 0.0 0.0 .O.0 0.783 0.0 0.0 0.0 0.0 p 8 30 0.0 0.697 0.0 0.0 0.0 0.774 0.0 0.0 0.0 0.0 rt 38 0.0 0.688 0.0 0,0 0,0 0.768 0.0 0.0 00 0.0 M-a 0.784 0.0 0.0 0.0 0.0 0 32 0.0 0.705 0.0 0.0 0.0 D 33 0.0 0.693 0.0 0.0 0.0 0.766 0.0 0.0 0.0 0.0 34 0.0 0.664 0,0 0.0 0.0 0.721 0.0 0.0 0.0 0.0 35 0.0 0.669 0.0 0.0 0.0 0.730 0.0 0.0 0.0 0.0 36 0.0. 0.654 0.0 0.0 0.0 0.701 0.0 0.0 0.0 0.0 37 0.0 0.631 0.0 0.0 0.0 0.648 0.0 0.0 0.0 0.0 38 0.0 0.627 0.0 0.0 0.0 0.634 0.0 0.0 0.0 0.0
- 39 0.0 0.625 0.0 0.0 0.0 0.626 0.0 0.0 0.0 0.0 40 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 49 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 42 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0
} 0.0 0.0 0.625 0.0 0.0 0.0 0.0 3 43 0.0 0.625 0.0 0.0 0.0 44 0.0 0.625 0.0 00 0.0 0.625 0.0 0.0 ' 45 0.0 0.625 .O.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 ' 46 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 47 . 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 4 48 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 49 0.0 0.025 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 4 50 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 4 59 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 52 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 ' 53 0.0 0.625 0.0 0.0 0.0 0.625 0.0 0.0 0.0 0.0 TOTAL t.50780*04 2.40580*05 2.55660605 s.5078D*04 2.4089p*05 2.5597D*05 5.1163 Deft ! ) i ? i i i f e . ,-, - - # ,-
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'O O TABLE 6,1-39 ESTIMATED RATE OF ENTRAINMENT_ LOSSES OF STRIPED BASS - LARVAE NO OUTAGE UNIT 1 UNIY 2' UNITS I & 2 MEAN ENTR MORTALITV- SWS CWS TOTAL MORTALITV SWS CWS TOTAL .COM88NED RATE Num8ER NUMBER .Num8ER RATE NUMBER NUMBER NUMGER TOTAL WEEM DENSITIES 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 -t 0.0 0.543 0.0 0.0 2 0,0 0.343 0.0 0.0 0.0 0.C43 0.0 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 3 0.0 0.0 0.0 0.0 0.0 4 0.0 - 0.543 0.0 0.0 -0.0' O 543 0.543 -0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 5 0.0 0.0 0.0 0.0 6 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.543 0.0 0.0 0.0' O.543 0.0 0.0 0.0 0.0 7 0.0 8 0.0 0.543 0.0 0.0 -0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 c.0 0.543 0.0 0.0 0.0 0.0 9 0.0 0.0 0.0 0.0 to 0.0 0.543 0.0 0.0 0.0 0.543 0.0 y, 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 y II 0,0. 0.0 -
12 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 13 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 e 14 0.0 0.543 0.0 0.0 0.0 0.543 b.0' O.0 0.0 0.0 9 15 0.0 0.543- 0.0 0.0 0.0 .0.'543 0.0 0,0 0.0 0.0 0.543 3.2429D*0J 4.45630*04 4.7776D*04 9.55520604 LJ 16 0.19 0.543 3.28290*03 4.4563D604.4.77760004 9.3775D*04 17 0.99 0.543 3.8532D603 4.3734D*04 4.68880*04 0.543 3.1532D*03 4.3734De04 4.6888b*04 C"h 0.543 2.28970e03 3.l?58DeO4 3.40480*04 0.543 2.2897D*03 3.0760De04 3.4050De64 6.8098D604 18 19 0.04 0.34 0.543 5.73600603 7.9287DeO4 8.5003D*04 0.544 0.544 5.7960D*03 6.60080803 7.9388D604 8.5027De04 9.86830904 9.8284D404 8.7003D*05 1.96470805 (f ss 20 0.40 0.544 6.6068D*03 9.4590D*04 9.889tDeO4 9.2262De04 29 0.99 0.544 3.0930D'03 4.29690e04 4.60620*04 0.5=6 3.09300603 4.3807De04 4.6200D*04 22 c.05 0.546 8.5326D*02 0.1888D*04 0.27400604 0.550 8.53260e02 9.4975D604 1.2829D*04 2.5570D*04 O 1.28310*03 0.6979D804 8.80920804 0.555 1.283tD*03 f.78990004 1.84120*04 3.6604D*04 e 23 0.07 0.548 2.0327D*04 9 24 0.04 0.558 6.688tDe02 9.40860603 1.0077D604 0.569 6.688tD*02 9.58 tide 03 0.02500604 0 25 0.08 0.556 9.5544D*04 1.3507D*03 8.4462D*03 0.578 9.55440'01 1.3897De03 1.4772De03 2.9234D*03 26 0,0 0.567 0.0 0.0 0.0 0.590 0.0 0.0 0.0 0.0 l 27 0.0 0.570 0.0 0.0 0.0 0.595 0.0 0.0 0.0 0.0 n 28 0.0 0.586 0.0 0.0 0.0 0.620 0.0 0.0 0.0 0.0 n 29 0.0 0.685 -0.0 0.0 0.0 0.668 0.0 0.0 0.0 0.0 y 30 0.0 0.645 0.0 0.0 0.0 0.656 0.0 0.0 0.0 0.0 n O.649 0.0 0.0 0.0 0.0 "- 38 0.0 0.606 0.0 0.0 0.0' 0 32 0.0 0.615 0.0 0.0 0.0 0.662 0.0 0.0 0.0 0.0 0.657 0.0 0.0 0.0 0.0 3 33 0.0 0.608 0.0 0.0 0.0 34 0,0 0.599 0.0 0.0 0.0 0.627 0.0 0.0 0.0 0.0 35 0.0 0.594 0.0 0.0 0.0 0.632 0.0 0.0 0.0 0.0 36 0.0 0.583 0.0 0.0 0.0 0.686 0.0 0.0 0.0 0.0 37 0.0 0.562 0.0 0.0 0.0 0.589 0.0 0.0 0.0 0.0 38 0.0 0.554 0.0 0.0 0.0 0.566 0.0 0.0 0.0 0.0 39 0.0 0.547 0.0 0.0 0.0 0.554 0.0 0.0 0.0 0.0 40 0.0 0.545 0.0 0.0 0,0 0.547 0.0 0.0 0.0 0.0 48 0.0 0.544 0.0 0.0 0.0 0.544 0.0 0.0 0.0 0.0 42 0.0 0.543 0.0 0.0 0.0 0.544 0.0 0.0 0.0 0.0 43 0.0 0.543 0.0 0.0 0,0 0.543 0.0 0.0 0.0 0.0 44 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 45 0.0 0.S43 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 46 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 47 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 48 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 49 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 50 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0,0 59 0.0 0.543 0.0 52 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 53 0.0 0.543 0.0 0.0 0.0 0.543 0.0 0.0 0.0 0.0 TOTAL 2.6896D*04 3.7353D*05 4.00420*05 2.68960*04 3.74300805 4.00490805 8.01620e0
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