ML20150F319
| ML20150F319 | |
| Person / Time | |
|---|---|
| Site: | New England Power |
| Issue date: | 09/30/1979 |
| From: | YANKEE ATOMIC ELECTRIC CO. |
| To: | |
| Shared Package | |
| ML20150F316 | List: |
| References | |
| NUDOCS 7910020420 | |
| Download: ML20150F319 (417) | |
Text
{{#Wiki_filter:_ . . - - . .. ____..- ... .- .- _ 4 P > APPENDIX G .
- THE ENVIRONMEhTAL IMPACT OF CONSTRUCTION AtID OPERATION
- OF THE C00 lit;G WATER SYSTEM
) FOR NEP 1 & 2, PROPOSED FOR CHARLESTOWN, RHODE ISLAND ON SELECTED REPRESE!ITATIVE IMPORTA?(T SPECIES SECTION 316, " TYPE II" DEMONSTRATION j Prepared for New England Power Company by . YANKEE AT0!!IC ELECTRIC COMPANY i
; ENVIRON!! ENTAL SCIENCES CROUP 20 TURNPIKE ROAD ,
WESTBOROUCll, MASSACHUSETTS 01581 ( September, 1979 1 ! a ) 1 1 i i I i 4 T J ie
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NE'P 1&2 ER TABLE OF CONTENTS Section No. Title Page 1.0 Introduction and Applicant's Impact Assessment Rationale C.1-1 1.1 Background C.1-1 . 1.2 Objectives C.1-1 13 Impact Assessment Rationale G.1-2
', 1.3.1 Da ta Requirements C.1-2 132 Impact Predictions C.1-3
( 1.3.3 Impact Assessment G.1-5 2.0 Existing Environment C.2-1 2.1 Physical / Hydrographic Description C.2-1 2.1.1 . Block Island Sound Ninigret Pond-C.2-1 General Description 2.1.2 Tempe ra ture, Salinity, Density Distribution C.2-2 2.1 3 Current, Tide, Wave Climatology C.2-4
. '2.2 . Summary Discussion of Regional Biota C.2-6 2.2.1 Net Plankton C.2-7 2.2 1.1 Phytoplankton C.2-7 -
t k
Sectics No. Titic - P;go
- 2.2 1.2 Zooplankton C.2-7 ,
t 2.2.1 3 Ic thyoplankton C.2-8 2.2.2 Benthos C.2-1L 2.2.2.1 ~ Rooted Aquatic Vegetation b.2-li 2.2.2.2 Inve r teb rates C.2-11
, 2.2.3 'Nekton C.2-12 3.0 Proposed Cooling Water System ,
C.3-1 3.1 Proposed Intake System G.3-2 3.2 Proposed' Discharge Syatem C.3-4 3 2.1 Discharge Description C.3-4 3.2.2 Discharge Operation Physical Ef fects C.3-5 ( 33 C.3-8 Biofouling Control 3.4 Chemical Discharges G.3-10 3.5 Cooling Water System construction Techniques C.3-13 4.0 Biological Effects of the Proposed Cooling Wa ter Systems on Representative Inportant .
, Species C.4-1 r
^
4.1 Methodology G.4-1 4.1.1 ,- Representative Important Species and the Rationale For Their Selection C.4 4.1.1.1 Basis for Selection of Species ' C.4-1 4.1.1.2 Threatened and/or Endangered Species C.4-3
' Sec t ion ::a'. Title Page ,
4.1.1.3 Nuisance G.4-3 4.1 1.4 Commercially or Recreationally Important G.4-3 4.1.1.5 Dominance G.4-5 4.1.2 Methods of Impact Analysis C.4-5 4 .1. 2.1 The Impacts of Construction G.4-5 4.1.2.2 The Impacts of Operation G.4-7 4.2 Impact Assessment G.4-18 4.2.1 Atlantic Menhaden (Brevoortia tyrannus) , G.4-18 4.2.1 1 Life History G.4-18 ( 4. 2.1. 2 Impacts of Construction C. 4-2 0
- 4. 2.1. 3 Impacts of Plant Operation G. 4-2 0 4.2.2 Bay Anchovy (Anchon mitchilli) G. 4-2 7 4.2.2.1 Life History G.4-27 4.2.2'2 Impacts of Construction G.4-29 4.2.2 3 Impacts of Plant Operation C.4-29 -
4.2 3 Silver Hake or Whiting (Harluccius bilinearts) C.4-33 4 2.3.1 Life liistory G.4-33 4.2.3.2 Impacts of Construction G.4-34 4.2 3 3 Impacts of Plant Operation G.4-35 4 2.4 Striped Bass (Morone saxatilin) G.4-38 8 4 2.4 1 Life Itistory G.4-30
.4.2.4.2 Impacts of Construction G. 4-4 0 U.*
4 Section No. Title Page 4.2.4.3 Impacts ut Plant Operatton C.4-40 ( 4.2.5 Bluefish (Pomatomus saltatrix) G.4-4'4 4.2.5.1 LLfe Itistory G.4-44 4.2.5.2 Impacts of Construction , G.4-45 4.2.5.3 Impacts' of Plant Operation G.4-45 i 4.2.6 Scup (Stenotomus chrysops) G.4-49 i
. 4.2.6.1 Life History G.4-49 4.2.6.2 Impacts of Construction G.4-50, 4.2.6.3 Impacts of Plant Operation G.4-50 4.2.7 Cunner (Tauto,tolabrus adspersus) G.4-54 1
( 4.2.7.1 Life History G.4-54
; 4.2.7.2 Impacts of Construction G.4-55 t
4.273 Impacts of Plant Operation G.4-55 4 4.2.8 Sand Lance ( Amcodytes americanus) G.4-58 i 4.2.8.1 Life liistory G.4-58 4.2.8.2 Impacts of Construction G.4-60 1 4.2.8.3 Impacts of Plant Operation G.4-60 4.29 Atlantic Mackerel (Scomber scombrus) C.4-65 4 4.2.9.1 Life History , G.4-65 4.2.9 2 Impacts of Construction G.4-67 4.293 Impacts of Plant Operation G.4-67 ( 4.2.10 Butterfish (Pepriltis t r inenn thus ) G.4-71
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Section No. Titl_e Page c 4.2.10.1 Life llistory G.4-71 4.2.10.2 Impacts of Construction C.4-72 4.2.10 3 Impacts of Plant Operation C.4-72 4.2.11 Winter Flounder (Pseudopleuronectes americanus) C.4-76 4.2.11.1 Life !!istory C.4-76 4.2.11.2 Impacts of Construction C.4-78
- 4.2.11 3 Impacts of Plant Operation .C.4-78 4 2.12 Blue Mussel (Mytilus edulis) C.4-88 9
4.2.12.1 Life llistory C.4-88 ( , 4.2 12.2 Impacts of Construction C.4-89 , 4 2.12 3 Impacts of Plant operation . C.4-90 4.2.13 Hard Clam (ttarcenaria mercenaria) - G.4-94 4.2.13.1 Life IIistory C.4-94 4.2.13.2 Impacts of Construction C.4-96
, 4.2 13 3 impacts of Plant Operation C.4-96 4.2.14 Long-Finned Squid (Loligo pealci) C.4-97 4.2.14.1 Life Ilistory C.4-98
. .4.2.14.2 Impacts of Construction C.4-99
. l 4.2.14 3 Impacts of Plant operation C.4-99 k 4.2.15 Sand Shrimp (Crannon septemsninosas) C . 4-10 7 4.2.15.1 Life Itintory C. 4-10 7 4.2.15.2 Impacts of Construction C.4-108 e'
Section No. Titio PJge 4.2.15 3 Impacts. of Plant Operation G.4-109 4.2.16 American Lobster (Itomarus aciericanus) G.4-115 . . 4.2.16.1 Life llistory G.4-115 4.2.16.2 Impacts of Construction G.4-117 4.2.16.3 Impacts of Plant Operation G.4-118 4.2.17 Eelgrass (Zostern marina) G.4-127 4.2.17.1 Life Ilistory G.4-127 4.2.17.2 Impacts of Construction G.4-128 4 2.17 3 Impacts of Plant Operation G.4-128 4.3 Other Impacts G.4-129' Cold Shock G.4-129 431 ( 4.3.2 Cas Bubble Disease G.4-130 433 flydrostatic Pressure Ef fects G.4-132 4.34 Skinnyfish Syndrose G.4-132 4.3.5 Premature Spawning C.4-133 4.3 6 Effects of Chemical and Biocide Discharges G.4-134 4.3 7 Effect of Thermal Backflushing C.4-136 5.0 Alternative Intake Systems G.5-1 5.1 Onshore Intake G.5-1 5.1.1 System Description G.5-1 - 5 1.2 Environmental Impacts G.5-1 , 5 1.3 Engineering Condinerations- G.5-2 ( 5.1 4 Summary: Onahore vs. Of f shore Intake G.5-2 ti
l j Section No. Title Page .
?
5.2 Far Of fshore Intake - G.5-3 5.2.1 System Description G.5-3 5.2.2 En'rironmental Impacts G.5-3 5.2.3 Engineering Considerations G.5-4
5.2.4 Summary
Proposed vs. Far Of fshore Intake G. 5 -4 6.0 Representative Important Species Impact Summaries and Master Ecosystem Rationale G.6-1 6.1 Representative Important Species Impact Summaries *G.6-1 6.1 1 Impacts of Construction G.6-1 6.1.2 Atlantic Menhaden C.6-2 6.1.3 Bay Anchovy G.6-3 6.1.4 Silver Hake G.6-5 6.1.5 Striped Bass G.6-6 . 6.1.6 Bluefish G.6-7 6.1 7 Scup G.6-8
. 6.1.8 Cunner G.6-10 6.1 9 Sand Lance G.6-11 6.1.10 Atlantic Mackerel G.6-12 6.1.11 Butterfish G.6-14 6.1.12 Winter Flounder G.6-15 6.1.13 Blue Mussel G.6-18 k 6.1.14 Hard Clam G.6-19 6.1.15 Long-Finned Squid G. 6-2 0 6 1.16 Sand Shrimp ,
G.6-21 6.1.17 'Americanl$bster. G.6-23
Sectica No. . 'Titic p;gg 6.1.18' Eelgrass C.6-24
. .(
6.2 Master Ecosystect Rationale C. 6-2 5 7.0 Bibliog raphy C.7-1 O O 2 t f
~
NEP 1&2 ER
- LIST OF ILLUSTRATIONS Figure No. Title G.2.1-1 Ba'thymetry of Greater Block Island Sound G.2.1-2 Bathymetry of Proposed Intakes and Dif fuser Area ,
G.2.1-3 General Bottom Character of Proposed Intakes and Diffuser Vicinity . G.2 1-4 Annual Block Island Sound Salinity Temperature ( Density Profile G.2.2-1 Baseline Survey Sampling. Stations G.2.2-2 Relative Utilization of Adjacent Of f shore Waters by Two Commercial Trawlers , G.3.0-1 Proposed Circulating Water System in Block Island Sound G.3.0-2 Intake and Discharge Tunnel Profiles in Block Island Sound G.3.1-1 Circulating Water Intake
- Structure a
tA
F1gure No. Title . l, G.3.2-1 P.oposed Discharge Structures in HLock Island Sound , G.3.2-2 Surface Temperature Rise Isotherms G.3.2-3 Cross-Sectional Temperature Isotherms
- G.3.2-4 Surface Temperature Rise Iso the rms
, - G.3.2-5 Cross-Sectional Temperature Rise Isotherms G.3.2-6 - Variations of Surface Isotherm Areas with Tidal Current G.3.2-7 Surface Temperature Rise Isotherms G.3.2-8 Surface Temperature Rise Isotherms ( G.3.2-9 Surface Temperature Risa Isotherms G.3 2-10 Surface Temperature Rise Isotherms G.3.3-1 Surface Temperature Rise Isotherms Backflushing 4 C.3.3-2 Surface Temperature Rise Isotheras Backflushing G.3.3-3 Surface Temperature Rise Isotheras Backflushing C.4.1-1 Example of Selected Species Rela'tive Temporal Abundance , and Thermal Characteristics G.4.2-1 Atlantic Menhaden Temporal Abundance at Block Island Sound Station A ( G.4.2-2 Distribution and Average Density of Atlantic Menhaden Eggs, 1974
,--e. - - - ~
Figure'N3. Title a G.4 2-3 Distribution and Average Density of Atlantic Henhaden Eggs, 1975 G.4.2-4 Distribution and Average Density of Atlantic Henhaden Larvae, 1974-1975 G.4.2-5 Distribution and Average Density of Atlantic Menhaden Larvae, 1975-1976 C.4.2-6 Atlantic Menhaden Relative Temporal Abundance and Thermal Characteristics
. G.4.2-7 Bay Anchovy Temporal Abundance at Block Island Sound Station A
( G.4.2-8 Distribution and Average Density of Bay Anchovy Eggs, 1974 G.4.2-9 Distribution and Average Density of Bay Anchovy Eggs, 1975 k . G . 4. 2-10 Distribution and Average Density of Bay Anchovy Larvae, 1974 G. 4. 2-11 Distribution and Average Density of Bay. Anchovy Larvae, 1975 C. 4. 2-12 Bay Anchovy Relative Temporal Abundance and Thermal Characteristics *
\
C. 4. 2-13 Silver llake Temporal Abundance at Block Island Sound Sta tion A-Xi
Figure Nos Title ( C.4.2-14 Diatrihutton and Averar... lienalty at St t ver 'llake Eggs, 1974 . C.4 2-15 Distribut ton and Average Density.of Silver llake Ef,gs, 1975 . t C. 4. 2-16 Distribution and Average Density of Silver llake larvae, .1974
. C.4.2-17 Distribution.and Average Density of '
. Silver Itake i.arvae, 1975 - I G . 4. 2-18 Striped 11 ass Relative Temporal Abundance I and '!hermal Characteristics - (> C.4.2-19 ' Bluefish Relative Terr. poral Abundance
- and Thermal Characteristics C.4.2-20 Scup Temporal Abundance at Block Island Sound Station A C.4.2-21 Distribution and Average Density of Scup Eggs, 1974 -
C.4.2-22 Distribution and Average Density of Scup 4 Eggs, 1975 1 C.4.2-23 Distribution and Average Density of Scup I,arvae, 1974 (
'C . 4. 2-2 4 Distribution and Average Density of '
1
. Scup I,arvae, 1975 4
f i t.
.. a . , . _._;_,.. ,. . . _ _ _ _ . ._ ._ ,,. . _ . . _ , . _ _ - . _ . . . . -._
4 5 Figv.ra No. Title (' G.4.2-25 Cunner Temporal Abundance at Block Island Sound Station A G.4.2-26 Distribution and Average Density of Lab' rid-Limanda Eggs, 1974 ' G. 4. 2-2 7 Distribution and Average Density of Labrid-Limanda Eggs, 1975 G. 4 2-2 8 Distribution and Average Density of Conner Larvae, 1974 s G.4.2-29 Distribution and Average Density of , Cunner Larvae, 1975 , G.4.2-30 Cunner Relative Temporal Abundance and
, Thermal Characteristics G.4.2-31 Sand Lance Larvae Temporal Abundance at Block Island Sound Station A G.4.2-32 Distribution and Average Density of
, Sand Lance Larvae, 1974-1975 -
. G.4.2-33 Distribution and Average Density of
._ Sand Lance Larvae, 1975-1976 i
, G.4.2-34 Atlantic Mackerel Temporal Abundance at Block Island Sound Station A
( G.4.2-35 Distribution and Average Density of Atlantic Macherel Eggs, 1974
Figure No. Title G.4.2-36 Distribution and Average Density of ' Atlantic thekeret E dgs, 1975 C . 4. 2-3 7 Distribution and Average Density of Atlantic Mackerel Larvac, 1974 G . 4. 2-3 8 Distribution and Average Density of
~ Atlantic Mackerel Larvae, 1975 .
G.4.2-39 Atlantic Mackerel Relative Temporal 4 Abundance and Thermal Characteristics G. 4. 2-4 0 Butter 51sh Temporal Abundance at Block
' Island' Sound Station A (
G.4.2-41 Distribution and Average Density of Bu t te r f ish Eggs", 1974 G.4.2-42 Distribution. and Average Density.of Butterfish Eggs, 1975 G.4.2-43 Distribution and Average Density of Butterfish I.arvae, 1974 G.4.2-44 Distribution and Average Density of Butterfish Larvae, 1975' G. 4 2-4 5 Winter Flounder Temporal Abundance at Block Island Sound Station A I G.4.2-46 Distribution and Average Density of Winter Flounder Larvae, 1974-L975 [
Figure Na. Title-G.4.2-47 Distribution.and Average Density of Winter Flounder Larvae, 1975-1976 , G.4.2-48 Winter Flounder Relative Temporal Abundance and Thermal Characteristics l G.4.2-49 Blue Mussel Temporal Abundance at Block Island Sound Station A - G.4.2-50 Distribution and Average Density of Blue Musssel Larvae per m3 , 1974-1975 . . G.4.2-51 Distribution and Average Density of Blue ( Mussel Larvae per m3 , 1975-1976 . G. 4. 2-52 Blue Mussel Relative Temporal Abundance and Thermal Characteristics , G.4.2-53' Squid Juvenile Temporal Abundance at Block Island Sound Station EB -B , 1977 G.4.2-54 Distribution and Average Density' of Squid Juveniles 1977 ,, G . 4. 2-55 Sand Shrimp Temporal Abundance at Block ( t Island Sound Station EB-B x V.
Figure Ms. Title " ( G.4.2-56 Distribution and Average Density ot Sand Shrimp Larvae per m3 (Surf ace)
- G.4.2-57 ~
Distribution and Average Density of Sand Shrimp Larvae per m3 (Bottom) G.4.2-58 Sand Shrimp Relative Temporal Abundance and Thermal Characteristics G.4.2-59 Lobster Tempo ral Abundance in Block Island Sound G.4.2-60 Distribution and Av'erage Density of Lobster Larvae - (Surface) 1977 G.4.2-61 Distribution and Average Density of Lobster Larvae
, (Bottom) 1977 G.4.2-62 _ American Lobster Relative Temporal Abundance ,
and Thermal Characteristics G.5.0-1 NEP 1&2 Intake Decision and Location
. Decision Matrix
4 NEP 162 ER LIST OF TABLES Table No. Title C.2.2-1 Summary of Block Island Sound Biological Sampling Program C.2.2-2 Summary of Ninigret Pond Biological Sampling Program G.2.2-3 Finfish Species Observed in Ichthyoplankton Collections , G.2.2-4 Mean Catch (per 100 m 3 ) of Selected Fish Eggs Taken at Stations NP A through NP E in Ninigret Pond Calculated for Monthly Periods, April 1974 - March ~ 1976 C.2.2-5 Mean Catch (per 100 m3) of Selected Fish Larvae Taken at Stations NP A through NP E in Niulgret Pond Calculated for Monthly Periods, 4 April 1974 - March 1976 Mean Catch (per 100 m3) of Selected Fish Eggs Taken at Stations G.2.2-6 BIS A through BIS D in Block Island Sound Calculated for Monthly Periods, April 1974 - March 1976 C.2.2-7 Mean Catch (per 100 m 3 ) of Splected Fish Larvae Taken at Stations BIS A through BIS D in Block Island Sound Calculated for Monthly Periods, April 1974 - March 1976 C. 2. 2- 8 Percent Abundance of Ichthyopla'nkton KV5L
G.2 3-1 Finfish and' Hacroinverteb rates Captured in Ninigret Pond and ( Block Island Sound, April 1974 - tiarch 1976 G.2.3-2 Catch of Two Commercial Trawlers, July 1974 - }brch 1976 G.2.3-3 Principle Nekton Species Taken by 45' Stern Trawler at Two Transects April 1975 - March .1976 G.3.2-1 Nearfield Thermal Plume Characteristics G.3.2-2 Transient Plume Characteristics G.3.4-1 Chemicals Discharged During Steam Generator Blowdown G.4.1-1 Representative Important Species List G.4.1-2 Entrainment of Eggs and Larvae of the Representative Species As'suming r 100% Power During Study Period , O G.4.2-1 Lobster Life Table Statistics 1
.6.0-1 Representative Important Species - Impact Summary i .
) 4 t i 6 xvut . O e
. . - . - ..- - . - .-.-.-.--------.--m .. a.-.,- , , - - , - . . . - - - - . .
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1 NEP 1&2 ER APPENDIX G j p 1 Tile ENVIRONMEWAL -IMPACT OF-CONSTRUCTION AND OPERATION OF TiiE COOLING e WATER SYSTEM FOR NEP 1 & 2 ON SELECTED REPRESENIATIVE IMPORTAE SPECIES 4 1 2
1.0 INTRODUCTION
AND APPLICANTS' IMPACT ASSESSMENT' RATIONALE 4 1.1 Background i l The Federal Water Pollution Control Act, as amended by the Clean Water Act of 1977, i
! requires that steam electric generating stations, such as the proposed NEP 1&2 plant, have the best available control technology for minimizing the discharge of pollutants.
l* Thi.s has been interpreted by the Environmental Protection Agency as requiring the use t
..I
.of a closed cycle cooling system for condenser cooling water. Under Section 316(a)
I of the Clean Water Act, however, an exemption f rom closed cycle cooling can be granted - 1 i if it can be demonstrated that the effluent limitations are "... more stringent than L , necessary to assure the protection and propagation of a balanced, indigenous population of shellfish, fish, and wildlife in and on the body of water into which the discharge , is to be made . . .". Section 316(b) of the' Clean Water Act, while not dealing with an s effluent, requires "... that the location, design, construction, and capability of cooling water intake structures reflect the best technology available for minimizing adverse environmental impact". 1.2 Obje ctives It is 'the objective of this Appendix to summarize information found elsewhere in the Environmental Report (ER) (NEP 162, 1976 as amended) and present additional analyses to address the requirements of both Sections 316(a) and 316(b). The format of the G.1-1 '
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NEP 1&2
' App' e ndix follows, as closely as practical, the Type II demonstration as proposed in
-[
the draf t technical guidance mnual dated May 1977 by the Environmental Protection Agency (EPA). Representative Important Species are those-designated by EPA for the proposed NEP 152 plant. This Appendix provides a concise and clearly documentable demonstration that the station and its proposed circulating water system meet or exceed the requirements of both 316(a) and 316(b). Presented herein are descriptions of the existing environment, the proposed circulating water system, analyses of the ef fects of the proposed. system on the representative important species, analyses of alternative intake design concepts and a summary and conclusion of Applicants' findings. In keeping with the spirit of the "Second Memorandum of Understanding and Policy Statement Regarding Implementation of Certain NRC and EPA Responsibilities" (40CFR60ll5). . this demonstration will be made a part of the Environmental Report, which is used to (.
~
fulfill the requirement of the National Environmental: Policy Act of 1969.. 1 1.3 Impact Assessnent Rationale The impact assessment rationale to be used in meeting the objectives described in Section 1.2 is one appropriate for a new power plant facility such as NEP 1&2' and are described below. 1.3.1 Data Requirements Species which reflect representative' biotic communities were ' evaluated and the appropriate ra tionale provided f o r their choice ( s e e S e c t io n 4.1.1).. Pertinent scientific literature and site specific environmental baseline studies were k reviewed to:
'C.1 .
----s , , , - - -, - -- - - - - - - - - -
e ~ r
NEP 1&2.
- a. Describe selected species with respect to their population size, distribution both spatially and temporally, fecundities, survivorship, life history
; characteristics, and interaction with the proposed operation of the plant.
Where possible, all life history stages for the selected species (e.g. , eggs and larval stages) and their respective requirements for survival (e.g. , food) were considered.
- b. Compile thermal tolerance data on the various life history stages of any given selected species.
- c. Ensure special emphasis be given to identify the ef fects on community function and structure within the influence of the proposed intake and/or discharge.
Where appropriate, evaluations of 'such parameters as entrainment velocity, siltation, scouring, thermal and mechanical stress we re considered. ( Engineering data relative to the design of the proposed NEP 162 plant are provided in Section 3.0. The intake geometry of the circulating intake system is described and illustrated in detail, along with information on intake velocities and rates of flow. Seasonal operation of the intake is described, in addition to cleani g and backflushing procedures which would be instituted. The station design and operation is characterized as it af fects the intake and discharge . of the circulating water system. Such operating parameters as temperature, time, flows as functions of seasonal load, f requency of occurrence and transient or nonsteady-state operation are addressed. The _ discharge geometry is describeo in detail and illustrated. Its measurements, i discharge velocities, and hydraulic characteristics are provided. t The oceanography of the water surrounding the proposed NEP 162 plant is presented. 1 C.1-3
NEP 1&2 Information' includes freshwater input, tidal flhetuations, : flushing rates, current ( descriptions, stratification cha racte ris tics a nd ambient ~ tempe rature da ta.
. Th5 therwil plume is described with respect to temperature, velocity, area distribution, and depth. The pertinent results of model studies conducted to simulate ef fluent j .
l _ discharge under'various -hydrological conditions and seasonal variations are also presented. t
. A description of the area affected by the intake and the discharge-induced ficid currents,. thermal. plume characteristics based on relative" field observations, and analytical' predictions are provided.
-1.3.2 Impact Predictions
! Two approaches for ' impact prediction are used in the demonstration: (
- a. quantitative projections of power plant impact by model simulation, and 1
- b. projection of power plant impact by data extrapolation derived f rom existing power plant environmental programs.'-
t For those species which are judged to have a potential for power plant related mortality i and for which existing population models are applicable, a quantitative projection of l this impact is made. The' particular model used for the prediction depends upon the information available to define the population and the information to quantify the perturbation. Models l reviewed by Horst (1975)' are representative of those' that are used for quantitative
- , predictions.
( i i Many of the more complex population dynamic models require a great deal of information for the affected population. Because of the nature of such input pa rame te r s , it is
..' G.1 -
NEP 1&2 difficult to make estimates from field studies, and many times information does not exist in the literature. When sufficient information is not available f or more sophisticated analyses, potential affects upon species populations will be quantitatively
. evaluated using more simplistic approaches. With respect to meroplankton entrainment, for example, these approaches include volumetric entrainment calculations or approaches similar to the technique suggested by llorst (1975) which translates the number of adults
~
, that would have resulted if no entrainment mortality were to occur and assuming no compensatory mechanisms.in the population.
Where possible, information on the environmental effects of thermal discharges and intake structures at existing power plants will be utilized in the prediction of potential biological impacts. 1.3.3 Impact Assessment ( To meet the objectives st'ated in Section 1.2, a detailed assessment / analysis of the biological, hydrographic, and engineering data was made. Basically, the approach to j be taken first involves defining the geographic regions of the aquatic environment potentially affected by the intake and thermal ef fluent of NEP 162 and using the + engineering and hydrological parameters listed in Section 1.3.1 above. Se.condly, having once identified these possible zones of influence, the likelihood of any given species encountering or residing within these zones of influence was then determined. 1 Projections of potential power plant- impact (utilizing the techniques identified in Section 1.3.2 above), were evaluated in part by comparing estimated numbers of affected biota to some reference base such as catch, statistics for commercial or sport species, . natural losses of biota due to predation, or year to year natural variations in population size. Species were then judged minimally af fected by the powe r plant if they represent only a . minor portion of the indigenous population. G.1-5
,r- . - - . . - - - - - . - , -
i1EP 162 Uhile such comparisons are useful in 1:apact assessment hy placing potential power plant biological impacts in perspective .with other natural or man-related sources of biological attraction, they were further integrated with: (1) information compiled on spacies' life history, geographic distribution and abundance, thermal sensitivity, growth, behavior, fecundity, and recruitment; and (2) environmental baseline data (which includes physio-chemical and biological data) collected f rom ecological studies at the t1EP.1&2 site, in order to properly evaluate the sensitivity of the species population to any ef fect of power plant operation. This approach ensures that the, proper consideration be given to potential ramifications at the various biological community 1cvels. By properly utilizing the approach outlined above, potential power plant impaccs and assessment of significance can be directed at the individual species, the species population, and the overall biological community, thus ensuring that adequate protection be provided to all biological regiras of the ecosystem. ( 4 C.1-6
, NEP 162 2.0 EXISTING ENVIRONMENT The following subsections describe the existing physical / hydrographic (Section 2.1) and biological' (Section 2.2) environments. We material incorporates data acquired from published lit'erature, the Applicant's baseline survey (1974-75), and subsequent studies conducted through 1978. The baseline data are described in detail in .the NEP I 162 Environmental Report Sections 2.2, 2.4, and 6.1 (NEP 1&2,1976), whereas tho' subsequent studies are individually referenced. 2.l~ Physical / Hydrographic Description 2.1.1' Block Island Sound and Nininret Pond - General Description The area'between Block Island, located 9 mile's of fshore, and the Rhode Isihnd coast defines Block Island Sotind (EIS) . The 400 square mile Sound (Figurc G.2.1-1) is open [ to adjacent water bodies on three sides - Rhode Island Sound to the cast, the Atlantic Ocean to the south, and Long Island Sound to the west - and has- a mean depth of 120 t f eet, the maximum depth being about 300 feet of f Fishers Island (Williams,1969) . The region of the proposed intakes and dif fuser (Figure G.2.1-2), however, is between 30 and 40 fect'and has a relatively smooth sea-floor punctuated only by occasional small shoals (Raytheon,1975).- We sea-floor character (Figure G.2.1-3) is Eenerally comprised of a sandy bottom with areas of grairel and boulders (URI,1978). The sub-bottom (upper' . 3 feet), likewise, is predominately sandy with the sand content ranging from 50 to 97 percent; gravel content, 'on the other hand, ranges from 0 to 21 percent, and silt content from 1 to 29 percent (Nacci,1979). No rivers of significant size reach the southern Rhode Island coast, but Harrag'ans'et Bay.to the cast is fed by four rivers an.d the names and Connecticut Rivers are located i to the ws t . In addition, several _ coastal ponds occur in the area, Ninigret Pond being one of the largest, no long, shallow Pond has a surface area of approximately 1560 G.2-1
1 NEP 1&2 or tidal variations (Raytheon,1975). Ninigret Pond , unlike the open Sound, exhibits a slightly.dif ferent thermocline
-structure. Salinity, for example, is generally lower and more . varied throughout the Pond, a result' of localized area runof f. Low salinity values (about' 25 ppt) occur during.
,the spring with the high.(about 29 ppt) occurring during the late summer or early fall.
Values, however, may vary throughout the Pond, depending on' the location to potential
- runof f sources (Fort Neck) or BIS water - i.e., in the vicinity of' the Charlestown Breachway.
The annual temperature cycle for .Ninigret Pond has a trend similar to the of fshore temperature cycle; however, the maximum and minimum variation is greater in Ninigret Pond. In particular, the average maximum summer temperature is about 4-6 F greater than the average maximum of fshore temperature. Conversely, winter average minimum (- temperatures, are about 20F degrees less than offshore temperatures. Unlike offshore conditions,- the thermal stratification in the pond is not as well defined, a result' of the shallowness of the Pond and wind-mixing. Short term variations, however, are more pronounced, especially in the ' r'egion'of the breachway.- Because of the intrusion of BIS water into Ninigret Pond on flood tide, large tidal and diurnal variations usually occur. Variations, for instance, of nearly 110F within one-hour have been recorded (Jacobson and Snooks, 1978). 2.1.3 Current. Tide. Wave climatology Currents in -the Sound are predominantely driven by the semidiurnal three foot tide, which enters from,the. east in the form of a progressive wave (Riley et al.,1952) . Current directions have a dominant oscillatory component in the east-west direction, but display strong variab'ility associated with stora events. Average current speeds in the vicinity of the proposed intakes and dif fuser range from 0.4 to 0.8 f eet per G.2-4
NEP 162 ( second (fps) for near-surface currents and 0.3 to 0.5 f ps for near-bottom currents, and generally increase with distance from shore' and decrease with depth (Raytheo' n ,1975) . Nontidal drif t rates in BIS determined from drif ter data range from 1.0 - 7.6 nai/ day (0.07-0.53 fps) for surface waters to 0.2 - 0.5 nmi/ day (0.01-0.04 fps) for bottom waters (Williams,1969; Cook,1966; Paskauskey and Murphy,1976; Collins,1976) . Recent and more long-term studies (Snooks and Jacobson,1979) have shown the annual average surface and bottom nontidal speed to be 2.3 nmi/ day (0.16 f ps) and 0. 35 nmi/ day (0.02 f ps). respectively. All the studies indicate surface water flow exhibits a complex seasonally variable pattern, but bottom water nontidal flow is generally westward throughout the year. Snooks and Jacobson (1979) showed that nontidal drif t speeds determined from current meterdata,whichareagoodrepresentationoftheflushingvelocity(Csanady,1979),( are generally always present. The nontidal speeds, for example, are greater than 0.05 ' fps, 0.10 fps, and 0.15 fps about 90, 80, and 60 percent of th'e time, respectively. These values concur with a dye study conducted in 1974 which showed the flushing ability of the discharge vicinity to be good, with little potential for background heat buildup (Brocard and Hsu, 1978). Winds generally account for the episodic wave activity in BIS. Accordingly, the wave climate varies seasonally, with more severe conditions generally occurring during fall and winter (Raytheon,19 75); however, because of the shape ~ of B.IS and the nearly unlimited fetch to the south and east, severe storms with easterly and southerly wind produce the highest waves'(Williams, 1969). Significant wave heights, however, are generally less than .1.5 feet 68 percent of the time, and less than. 3 and 5 feet 92 and 98 percent of the time, respectively. ( G. 2 -5
NEP 1&2 t Unlike the Sound, currents within Ninigret Pond are not normally driven by the tide, which has a small range of about 0.4 feet (Raytheon, 1975), but instead by the wind. Consequently, Pond currents can best be described as episodic, with many irregularities produced by the Pond's shallowness. Flushing of the Pond , on the other hand , is periodic. Studies conducted at the Charlestown Breachway (Raytheon, 1975) indicate that between 12 and 18 percent of the volume of Ninigret Pond is discharged through the Breachway on each ebb tide, with maximum instantaneous flows typically between 2000 and 3000 cfs, which correspond to maximum current speeds of 3 to 4 fps. Coincidently, the average flow rate over an ebb discharge from the Pond is similar to the design NEP 1&2 cooling water flow rate, or 1907 cfs. Lastly, a dye study performed at the Charlestown Breachway indicated that only 10 percent of the water discharged from Ninigret Pond returned on flood tide. Hence, approximately 11 percent of the pond volume is exchanged during each tidal cycle (Raytheon, 1975). 2.2 Summary Discussion of Regional Biota he following subsections describe the results of the collection of baseline ecological data prior to construction. The methods, frequency, and locations utilized for the collection of the biological field samples are outlined in Tables G.2.2-1 and G.2.2-2. Samples were collected at stations depicted in Figure G.2.2-1. Block Island Sound and the waters in the vicinity of NEP 1 and 2 are north-temperate, coastal, salt-water environments. Both marine and estuarine species are found in the region. Here are no aquatic species unique to the area that are known to be rare or endangered. We species' composition of plankton changes in accordance with a seasonal. succession typical of north-temperate, coastal waters. Benthic biota are, for the most part, resident in the area throughout the year, though' their numbers and distribution G.2-6
,, m -- -
NEP 1&2 ( may be influenced by spawning or other factors.. Most of the pelagic fishes are seasonal in their occurrence. ' 2.2.1 Net Plankton 2.2.1.1 mytoplankton Approximately 114 species of phytoplankton and protozoans have been identified from the Ninigret Pond-Block Island Sound study area, with diatoms and flagellates most abundant. Dinoflagellates, ciliates and the group identified as "others" were relatively scarce. In Ninigret Fond, Chaetoceros sp., Thalassiosira sp., p eietonema costattsa, and Heterocapsa triquetra were most abundant during much of the year. In Block Island Sound, the dominant species composition was similar to that of Ninigret Pond with the exception that Corethron criophilum replaced H. triquetra. (. Total phytoplankton densities in Ninigret Pond and Block Island Sound varied seasonally. a The standing crop of phytoplankton was considerably higher in Ninigret Pond than that measured at the Block Island Sound stations. With the exception of early summer, primary productivity (rate of carbon uptake) measured in Ninigret Pond and Block Island Sound was similar and in general agreement with previously reported values. ' haring the early summer months, rate of carbon uptake was somewhat greater at the Block Island Sound stations. 2.2.1.2 Zooplankton Zooplankton and phytoplankton were collected and analyzed simultaneously. By subjecting the data to several types of analysis including.a factorial analysis of variance, the following conclusions were reached; k
- a. The standing crop of zooplankton was generally larger at the Ninigret Pond stations than at the Block Island Sound stations. Maximum concentrations G.2-7
, - . - . - ._- .u
'NEP 1&2 of zooplankton were attained during the summe'r months in the Pond and, to a lesser degree, ic the Sound.
9
- b. The zooplankton populations in Block Island Sound were dominated. by crustaceans; copepods were the most abundant taxa (particularly Acartia tonsa, h clausi, Pseudocalanus minutis and Oithona spp.) . While copepods were usually the dominant fo rm in Ninigret Pond as well, they were occasionally less abundant than polychaete, bivalve and gast ropod larvae.
- c. At any given station in either Block Island Sound or Ninigret Pond, the zooplankton was uniformly distributed both diurnally and throughout the water columns.
- d. Within Block Island Sound there was no appreciable inter-station species abundance variation.
- e. Within Ninigret Pond most of the results indicate a uniform distribution of the various species. Near the breachway (Station NP-C), however, total i
population densities were significantly lower. 1
- f. Block Island Sound and Ninigret Pond frequently had dif ferent dominant j species. An interaction between the Sound and.the Pond was demonstrated by the species composition at Station NT--C; zooplankton characteristic of both water bodies was found here.
, 2.2.1.3 Ichthyoplankton Ichthyoplankton were sampled more frequent!1y than any other taxa 'during the course of
~
j this study. The species identified as eggs, larvae or juvenile in Ninigret Pond and l Block Island Sound are presented in Ta* ole G.2.2-3. I G.2-8
NEP 1&2 ( The most abundant species of fish eggs collected in Ninigret Pond are presented by month in Table G.2.2-4* and the most abundant species of fish larvae are presented in Table G.2.2-5. The species of fish depicted in these two tables represent over 98% of the year's total catch.
; The Labrid-Limanda group (tautog, cunner, and yellowtail flounder) probably do not have significant breeding populations in Ninigret Pond. This conclusion was reached for several reasons:
- a. Due to the scarcity of suitable (rocky) habites, comparatively f ew adult tautog (Tautoga onitis) and cunner (Tautogolabrus adspersus) were captured.
- b. The yellowtail flounder (Limanda ferruginea) is an offshore species and was not collected in Ninigret Pond.
(-
- c. 'The eggs of the labrid-Limanda group were concentrated at Station NP-C (Figure G.2.2-1), and, therefore, abundance was apparently affected by tidal exchange throtch the breachway.
With the exception of the Atlantic mackerel (Scomber scombrus) which probably does not breed in Ninigret Pbnd, the other species of fish presented in Tables .G.2.2-4 and G.2.2- , 5 appear to spawn in the extremities of the Pond; their eggs were least abundant at Station NP-C which is adjacent to the breachway (Figure G. 2. 2-1) . .It is possible, "During a recent quality control check of environmental data, it was discovered that all Ninigret Pond ichthyoplankton data (Block. Island Sound data were not affected) were in error by a factor of 1.56 due to utilization of an incorrect flow meter conversion fac' tor. Therefore all Niniget Pond ichthyoplankton , . data presented in this document should be multiplied by 1.56 to obtain the correct densities. This et ror does not affect I ' impact assessments presented in Section 4.2 since only Block I Island Sound data were used. G.2-9
NEP 1&2 however, that th'e reduced numbers observed at Station NP-C were the result of dilution f rom the tidal exchange through the breachway.
< Winter flounder (Pseudopleuronectes americanus) led each year's catch of fish larvae in Ninigret Pond. The dominant summer species were the silversides (Menidia spp.) and the anchovy (Anchoa spp.). These three taxa accounted for more than 95% of the year's total catch of ichthyoplankton in Ninigret Pond.
The most abundant ichthyoplankton species collected in Block Island Sound are presented by month in Tables G.2. 2-6 and G. 2. 2-7. The average percent contribution of the major species is presented in Table G.2.2-8. The most abundant species of ichthyoplankton present in Block Island Sound was the Atlantic mackerel (Scomber scombrus), which, during 1974 and 1975, accounted for an average of 41% of the eggs and 27% of the larvae. This species was more abundant at the of fshore stations than at the inshore stations. i ( The Labrid-Limanda group was the second most abundant group in the egg collections. This group, together with the mackerel, accounted for an average of 92% of the eggs end 64% of the larvae. Other large contributions to the larvae in Block Island Sound were the anchovy, winter flounder, and sand lance-( Ammodytes spp.) which accounted for additional averages of 14%, 4%, and 4%, respectively. These three species were not
. irportant in the egg collections.
A preliminary survey of lobster larval density was conducted in 1976 and an intensive
~
sampling program was conducted to assess the density of squid juveniles and lobster larvae during 1977 (Table 2.2.2-1) . In general, lobster were more abundant at the surface and during the daytime samples; they were more abundant offshore during during 1977 and inshore during 1976. Squid j uveniles were more abundant inshore, near the bottom and at night.- t Larval stages of sand shrimp were present year round in Block Island Sound with major i G.2-10
NEP 1&2 gbundance levels occurring f rom April through November. Overall abundance was higher ( in near bottom waters than in surface waters with evidence of diel vertical migration. Dur'ing- the day larval densities were higher in near bottom waters, whereas, at night larval densities appeared to increase near the surface. 2.2.2 Benthos 2.2.2.1 Rooted Aquatic Vegetation Emigrass (Zostera marina) was the only spermatophyte collected. Maximum and minimum celgrass densities occurred during mid-summer and late winter, respectively. Zostera wIs relatively scarce near sampling Stations NP-A and NP-D. This reduced density.may bs partially attributed to the reduced tidal flow in these areas. Zostera was not observed in Block Island Sound. 2.2.2.2 Invertebrates (~ The benthos of Ninigret Pond consisted mostly of relatively small organisms; many of these live in close association with the extensive eelgrass (Zostera marina) beds. Conspicuous in this group were polychaete worms, crustaceans of the order Amphipoda, cnd relatively small gastropods and pelecypods. These populations, of importance in the food chain of the Pond system, tended to be more varied along the relatively shallow cnd sandy margins of the Pond than in the deeper areas characterized by sof t bottom. . Included in the benthos of Ninigret Pond were small numbers of American oyster (Crassostrea virginica), bay scallop (Argopecten irradians), hard clam (Mercenaria mercenaria), and ceft clam (Mya arenaria). The larval forms of these species are planktonic and their cccasional presence in the plankton of Block Island Sound indicates that they may be flushed into the Sound by tidal exchange, not only from Ninigret Pond, but also 'from ( e Narragansett Bay and the other salt ponds along the Rhode Island coastline. Since these G.2-11
-- ,a --
NEP 162 species do not become successfully established in the Sound, at least fn terms of providing a commercial or even a recreational fishery, it is presumed that the larvae swept into the Sound are lost and contribute little or nothing to the fishery.
~
The benthos of Block Island Sound appeared to be considerably more diverse than in the Po nd . During a twelve-month period beginning in March 1975, a total of 269 species were identified in Block Island Sound as compared with 106 species identified in Ninigret Pond; those identified consisted of 149 species of polychaetes in the' Sound, as compared with 49 in the Pond; 87 species of crustaceans in the Sound as compared with 44 in the Pond; and 33 species of gastropods in the Sound, as compared with 13 in the Pond. Most of the Pond samples were collected from sof t-mud bottom. Although large and valuable invertebrate species such as the lobster (Homarus americanus), mahagony quahog ( Artica islandica), and surf clam (Spisula solidissima) were fished commercially in' the Sound off martestown Beach, these were not collected in any particular abundance during this survey. As was true for the benthic populations of Ninigret Pond, the numerically dominant forms in the Sound were polychaete worms, amphipods, and small mollusks, the 5 last of which included juvenile blue mussels (Mytilus edul's). i Statistical analysis of the data collected indicates that there was little or no along-shore variation in the benthic community. In an onshore to offshore direction, there was a highly significant community dif ference: density and diversity were lower in the 10-I j 30' water depth regions than in the 40-60' water depth regions. 2.2.3 Nekton During the two year period from April 1974 through March 1976, a total of 75 species of finfish and 2 species of motile invertebrates (lobster and squid) were collected in Nin'igret Pon'd and the area of Block Island' Sound depicted in Figure G.2. 2-1; 56 ( species have been identified in Ninigret Pond; 51 species in Block Island Sound; and
- 29 species were common to both areas (Table C.2.3-1) .
G.2-12
- - - - - - ----~ , --w, e
NEP 1&2 ( Those finfish species with'in the study area, which were found primarily in Ninigret s Pond, are eurythermal and euryhaline. ney prefer shallow water and, in many cases, are non-migratory. The dominant resident species were the silverside (Menidia spp.), killifish (Fundulus spp.), sheepshead minnow (Cyprinodon variegatus), sticklebacks (Apeltes quadracus and Gasterosteus aculeatus) and the northern pipefish (Syngnathus fuscus) . During the winter, spring, and f all spawning seasons, v.i n t e r flounder (Pseudopleuronectes americanus) were abundant in the Pond. Highest catches were recorded at Station NP-C (Figure G.2.2-1) followed by Stations NP-A, MP-B and NP-D. He fewest winter flounder were recorded at Station NP-E. Other species of fish found seasonally in moderate numbers include the menhaden (Brevoortia tyrannus), herring (Clupea harengus), and bluefish (Pomatomus salatrix). Neither lobster nor squid were collected in any Ninig ret Pond samples. Quantitative data on the nekton in Block Island Sound were obtained from three commercial trawlers. Two of the fishermen were requested to provide (1) information on the frequency with which they trawled the grid area depicted in Figure G.2.3-1 and (2) information on the total catch within the area. From the frequency of utilization based on 497 tows (Figure G.2.2-2), it is apparent that at least two commercial fishermen definitely prefer to fish well offshore. He greater part of the dragging took place in water deeper than 60 feet and most' of the dragging was in water 90-100' deep. Little or no dragging was conducted inshore because bottom conditions were generally
~
unfavorable. Some commercial line-trawling for cod was conducted near the Ninigret , Pond breachway during the winter months. he catch' of the two' commercial trawlers is pres ented in Table G.2.3-2. By f ar, the largest component of the commercial catch was ( silver hake which accounted for 29% of the catch by weight. B is species plus other G.2-13
1 . NEP 162
; 1 members of the cod family accounted for 42% of the total catch by ~ weight. ' Other major components of.the commercial ca tch we re skate, herring, and flounder.
j j~ A third commercial trawler (45' stern trawler, chartered with a biologist on board)
+
provided quantitative data on the species composition at two transects; one between b Stations BIS-A and B' and the other near Station BIS-C (Figure G.2.2-1). A total of i 31 species of finfish plus squid and lobster were taken at these stations. The 12 species listed in Table G.2.3-3 account for approximately 98% of the total catch; butterfish, windowpane, scup, little skate, winter ' flounder and squid account for 87%-
- of the total.
Differences in the relative importance of the species taken by the commercial trawlers, as presented in Tables G.2.3-2 and G.2.3-3, reflect dif ferences in (1) number vs. weight as indicators, (2) location fished, and (3) trawling technique. These differences also ( reflect the fact that one trawler was~ sampling while the other two trawlers were p selecting, for economic reasons, when and where they fished. A gill net was set on the bottom near Station BIS-A f rom ' September 1974 through March- , 1975. Unfortunately, the net was subject to severe fouling by seaweed and the program i' was discontinued. During the period when it was set, the most frequently caught fish i in the meager catch udre scup (Stenotomus chrysops) and the northern sea robin -(Prionotus i ; j carolinus). According to Sisson (personal communication), the area between the Quonochongtaug Pond 4 i breachway and Ninigret Pond breachway receives heavy recreational fishing pressure. This area includes the barrier beach, the near-shore area of f East Beach, the breachways
- ,, and Ninigret Pond.
i( i G.2-14
, a. _ _ . _ _ . , _ . _ . . _ . , . . . . , _ , ._ -- . - _ . . , - _ _ _ .__ _ _ _ _ _ - _ _ . . . - . _
4 NEP 1&2 The beach area from Quonochongtaug Pond breachway to the Ninigret Pond breachway is utilized by mobile sportsmen who gain access to the area via East Beach Road. Typically, these mobile sportsmen surf cast for striped bass (Morone saxatilis) and bluefish (Pomatomus saltatrix) from spring through the fall, with the peak activity in the months of September, October and November. Some sportsmen in small boats, as well as larger char ter boats , fish the area o f f East Beach for bluefish , summer flounder (Paralichthys dentatus) and striped bass. The area is considered poor for cod fishing and the sportfishing activity from boats is generally confined to the summer months. Additionally, there is a small recreational spear fishery for blackfish or tautog (Tautoga onitis). The area of the Ninigret Pond breachway, including the riprap sides of the breachway and the jetties, receives very heavy fishing pressure from early May through November regardless of .he availability of fish. Bis area has both public access an.d parking. ( 1- Sportsmen in this area fish for striped bass, bluefish and summer flounder or fluke during the spring and summer. Additionally, winter flounder (Pseudopleuronectes americanus), are pursued during their fall movement into the pond'and spring movement out of the pond. In Ninigret Pond, the most important sport fish species is the winter flounder. During the fall and spring, a large recreational fishing activity centers around the winter flounder. There are a few marinas with small boat rental facilities that provide the sportsmen with access to the pond. Additionally, some of the sportsmen pursue striped bass in the spring and snapper blue fish during the summer in the pond. Besides finfish, there is an active recreational shellfishery in Ninigret Pond. The hard clam or quahog (Mercenaria mercenaria) is the dominant species fished. Here is ,
\ ,
some digging for sof t clams or long necke (Mya arenaria), -but beds are few and densities low. 'Ninigret Pond contains a small naturally setting population of oysters (Crassostrea G.2-15
4 NEP 162 acres, depths of 8 feet o.r less, and is generally divided into western, central , and northern basins. The northern basin, known as Fort Hill Pond, represents the drowned valley of a glacial meltwater stream, whereas the rest of the pond is a flooded portion of the outwash plain separated from the ocean by a barrier beach. Composition of the pond bottom sediment (top meter) is mostly silt topped over by a thin (1-10 cm) silty sand layer (Dillon, 1964; NEP, 1976). The Pond is connected to the east by a narrow neck to nearby and smaller Green Hill Pond, which has an approximate surface area of 420 acres. Freshwater runof f to the Pond system is appreciable (about 44 x 103 m3 / day) and enters mostly. along the northern shore (Conover,1961) Exchange between Ninigret Pond and Block Island Sound is provided by the Charlestown Breachway, a 100 foot-wide inlet artificially stabilized in its present configuration in 1952. The waters of Block Island Sound, like the adjoining Rhode Island and Long Island Sounds, are derived, as described by Riley (1952), f rom a mixture of continental of fshore shelf l' water and coastal runof f brackish water. The slow south-westerly drif t of water al.ong the continental shelf south of New England is partially diverted around either side of Block Island entering BIS mostly as low temperature, high salinity bottom water. The brackinh nearshore water tends to spread over the surf ace, forming a fresher layer. As the shelf water moves shoreward, it is continuously f reshened by mixing with the runoff. The inflow of saline water near the bottom is balanced by an outflow of the f resher surface water which passes out of BIS, to some extent south of Point Judith, but mostly between Block Island and Montauk Point. 2.1.2 Temperature, Salinity, Density Distribution The distribution of BIS temperature, salinity and densit'y (Figure G.2.1-4) results from a complicated interaction of currents and mixing processes generated by tides, winds, - bathymetry, and meteorological ef fects. Measured v11ues of salinity, for example, range from 29.00 to 33.00 ppt with surface salinity values less than botto'm salinity values G.2-2
I NEP 1&2 (Williams, 1969;,Raytheon, 1975; Snooks et al., 1977). The seasonal range of average ( calinity, however, is only about 1 ppt, with a minimum in late spring (about 31.0) and a maximum in autumn about (32.2 ppt) . A vertical gradient of salinity between surface and bottom of about 0.5 to 1 ppt is usually present, but may be as large as 2 ppt. Horizontal salinity gradients of 1 ppt over an area extending 2 to 3 nautical miles are also common. Tidal variation of salinity, however, is usually less than 0.5 ppt. Block Island Sound temperatures, on the other hand, undergo a more distinct annual cycle with average maximum surface values occurring in August (68-700F) and minimum values occurring in February (34-380F) . In addition, a seasonal thermocline develops. Surface to bottom thermal gradients develop in April, reach maximum values (8-120F) in August, rapidly dissipate to near isothermal conditions by late September and generally increase with distance offshore (Raytheon,1975; Snooks et al.,1977). The water column generally has a slight positive thermal gradient ,(about.10F warmer on the bottom)~ between October . to December, a resul't of the lag between surface and bottom cooling, but is nearly 3 isothermal thereafter until the spring. . Tecperatures in shallow (30 f t) nearshore regions cool and warm more quickly than temperatures at deeper (60-90 f t) offshore regions. Tidally induced variations in temperatures generally are of the order of 1 to 30F (Raytheon, 1975) but may be as high as 130 F at the entrance to Minigret Pond (Jacobson and Snooks, 1978). The density structure of the Sound generally is a reflection of the temperature regime. Consequently, maximum value's occur during the winter (about 26 sigma-t) and minimum values during the stamner (22-24 sigma-t) . The dif ference in density between the surface and the bottom -water, however, is at a minimum in winter (about 0.5 sigma-t) and at a maximum in summer (about 1.0-1.5 sigma-t) . This vertical dif ference between surface and bottom is fairly constant and hence no pronounced pycnocline develops. In addition, densities generally increase with distance from shor.e, but show no consistent lateral G.2-3
NEP 1&2 s virg in ic a) . Recreational harvesting oysters is permitted from September 15 through May 15. Bay scallop ( Argopecten irradians) populations within the pond are erratic, but when the population is up, a sizeable recreational fishery exists. Additionally, there is a summer blue crab (Callinectes sapidus) fishery. ( e G.2-16
NEP 1&2 30 PROPOSED COOLING WATER SYSTEM ( The heat dissipation system for NEP 1 & 2 is a once-through offshore intake and diffuser
~
system. His heat dissipation concept has been selected for NEP 1 & 2 on the basis of environmental, engineering, na' d economic considerations. W e circulating water system for the two units are combined in- a single intake tunnel and discharge tunnel for both units. Figures G.3.0-1 and G.3.0-2 show the route and profile of the circulating water system. All normal heat dissipation functions for the plant are performed by this system; it provides heat removal from the main condensers and service water heat exchangers. Cooling water is taken from and returned to the waters of Block Island Sound at of fshore intake and discharge structures located south of East Beach near Charlestown, Rhode Island. We physical, . chemical and hydrological descr.iption of this body of water { 4 including its natural temperature pattern is presented in Section G.2.1 and ER Section 2.4. 4 he main objective in the selection of this heat rejection system was minimizing the potential environmental impact. Special consideration was given to the protection of , terrestrial and .squatic life that now inhabit the area. Also, it was specified that the selected system of heat dissipation would not provide hazards or impediments to highway, ship or air traffic in 'the region. he original proposed circulating water cysten has been revised from a piped system to a tunnel system described herein. Tunnels will be employed unless borings and other ghotechnical investigations prove that the concept is not feasible. He quantity of heat dissipated by each unit for condenser cooling is approximately 8 x 109 Btu / hour during full load normal operation. Within limits set by turbine perfonnance, the generator cycle can be modified by either limiting the amount of cooling I a G.3-1
- . - _ _ _ . - . - ~. -_. -- - . .-
NEP 1&2
~
water flow and having a high condenser temperature rise or having a greater flow with a lower temperature rise. To minimize pumped entrainment impacts on bio ta , NEP 1&2 is designed with a high condenser temperature rise and as low as practicable a cooling water flow, nominally 406,000 gpm per unit for condenser cooling. An additional flow of approximately 22,000 gpm per unit for the service water cooling is used to remove heat from the condensers and service water heat exchangers. Consequently, the total flow is 428,000 gpm per unit and 856,000 gpm for both units. The resulting temperature rise for NEP 1&2 is 370F. h us, NEP 1&2 will have one of the lowest water usage per kilowatt of any large power plant in the United States with once-through cooling. here is no in-plant consumptive use of cooling water. 3.1 Proposed Intake System.
- he intake system includes three identical offshore submerged intakes, one 18 foot inside
( diameter tunnel, an intake transition structure and a pumphouse located on the site. he nearshore intake structure is located 2,000 feet south of East Beach where the water depth is approximately 30 feet. We spacing between intakes is 110 f eet. At this location, the depth to bedrock is 95 feet resulting in an overburden depth of 65 feet. h e velocity of inflow at the point where water enters the inlets is no greater than
~
1.5 fps. His inlet velocity was selected af ter considering several factors which were judged to have an influence on the potential for finfish entrapment at NEP 1 & 2. Rese factors were: the ambient currents in the vicinity of the proposed intake ; research results from studies on the ef fect of various inlet velocities on fish entrapment for offshore cooling water structures; and the swimming capability of finfish found in the general region of the proposed intake location. This inlet velocity is rapidly i attenuated with distance from the inlet opening. his low approach velocity allows normal movement of fish in the area and reduces the possibility of fish entrapment and bottom scouring. Experience with of fshore intake structures along the coast of
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G.3-2
NEP 1&2 California indicates that a horizontal inflow current has much less potential for fish ( entrapment than a vertical current. A horizontal inflow direction about an offshore intake structure is maintained by means of a velocity cap. The velocity cap allows water to enter the intake opening f rom only a horizontal direction and has been demonstrated to reduce fish entrapment by a much as 95 percent at the offshore intakes of some power plants. Figure G.3.1-1 shows the design of the offshore velocity cap intake structure. From the inlets, the cooling water flows thrcugh the 18 foot I.D. intake tunnel about 6,200 feet into the pumphouse located at the plant site. He time of travel through the intake tunnel at the design flow rate of 856,000 gpm is about 14 minutes at an average velocity of about 7.5 f ps. he intake tunnel is constructed with an 0.5 percent slope toward the land to allow gravity flow of water seepage toward the plant during construction. He intake tunnel has a centerline elevation'of 170 feet below mean sea ( level (MSL) at the ocean end and 200 feet below MSL at the plant. Figure G.3 0-2 presents a profile of the intake tunnel. At the plant site, the flow passes from the intake tunnel into the intake transition structure which is a rectangular reinforced concrete box. The flow then passes through four butterfly valves (two for each unit) and enters two buried fiumes which flow into the circulating water pumphouse forebay. We pumphouse and forebay are divided by a concrete wall which also divides the two inflow flumes; each serves one unit. He pumphouse located on the site contains six circulating water pumps, three for each unit. Each ptsap is rated for 140,000 gpm flow at a 75 foot pumping head. Also contained in the onshore pumphouse structure are six vertical traveling screens (one for each pump), which divide the large forebay from the individual pump bays, and appropriate (' hydraulic equipment such as v .t i v e s , s t o p l o g s , and screen wash pumps. G.3-3
NEP 1&2 From- the pumphouse, the circulating water flows to the condensers through two buried pipes (one per unit) . The circulating water passes through the condensers and then flows to the discharge transition structure via buried pipes. Water is returned to ocean via an 18 foot inside diameter tunnel. The temperature of the circulating water
. flow is raised about 370F as_it passes through the condensers and heat exchangers.
3.2 Proposed Discharge System 3.2.1 Discharge Description.
'Ihe discharge side of the NEP 1&2 cooling system consists of buried on-site pipes leading f rom the condensers and heat exchangers to the discharge transition structure, one 18 foot I.D. discharge tunnel and a submerged multiport dif fuser. Af ter flowing through the condensers and the service water heat exchangers, the cooling water flows to the discharge transition structure and then approximately 6,500 feet through the 18 foot I.D. discharge ttanel to the submerged of fshore dif fuser. Travel time from the discharge transition structure to the diffuser for design rated flow is about 14.5 minutes a t approximately 7.5 fps. We discharge tunnel is constructed with an 0.5 percent slope toward the land to allow gravity flow of water seepage toward the plant during-construction. The discharge tunnel has a centerline elevation of 180 feet below MSL at the ocean and 210 feet below MSL at the plant. Figure G.3.0-2 shows a profile of the discharge tunnel.
Se heat dissipation system discharges into the water of Block Island Sound from diffuser nozzles located approximately 2,400 to 3,600 feet of f hore south of East Be ach . We discharge tunnel is connected to the diffuser by vertical riser shaf ts. Hyd rothermal 1 model studies (ER Appendices C1& CIA) have been undertaken to determine the design and
. location of the submerged multiport discharge dif fuser. Many variations of nozzle
( apacing, number and alignment of nozzles, orientation of dif fuser manifold and discharge G.3-4
NEP 1&2 velocity are possible for any given offshore discharge location. he purpose of the model studies was to develop a suitable dif fuser design which would produce the desired thermal discharge performance. A staged diffuser 1200 feet long was selected as the optimum dif fuser type for NEP 162 based upon an evaluation of historical model results and the of fshore hydrography at the NEP 1&2 site (Figure G.3.2-1) . A staged dif f user is a dif fuser whose axis is perpendicular to shore whose nozzles are directed essentially offshore. As proposed, the diffuser will start at the top of the discharge tunnel riser shaf ts beginning in approximately 31 feet of water, and consist of two 14 foot I.D. parallel pipes - one extending 600 feet seaward, the other extending 1,200 feet seaward. Each dif fuser will have 17 equally spaced two-foot diameter nozzles, each having an exit velocity of 18 fps. H e diffuser nozzles are angled up 20 from horizontal and alternate 20 degrees east and west of the diffuser axis. he nozzles for the 600 foot dif fuser ' start at ( the riser shafts; the nozzles for the 1,200 foot diffuser start 600 feet seaward of t.he ri'ser shafts. Thus, the total length of the dif fuser for NEP 1 & 2 is 1,200 feet. 3.2.2 Discharge Operation Physical Ef fects. He staged diffuser selected induces rapid mixing of the ambient water with the heated discharge water. He receiving water at the site is subject to changes in tidal elevation as well as current agnitude and direction. ne water current direction is predominately parallel to the shore line and has a maximum observed speed of about 1.6 fps. Because the initial temperature reduction of the thermal discharge for a given water depth is dependent on the momentum of the discharged jet as well as the magnitude and direction of ambient current, a staged dif fuser takes best. advantage of the ambient current condition. Since the performance of the diffuser is dependent on the magnitude ( of the ambient current, the size of a given isothe'rm varies with the ambient current and tidal stage as shown in Tables G. 3. 2-1 and G. 3.2-2.
, G.3-5
NEP.1&2 Two hydrothennal models are required' to predict thermal discharge behavior. h e region near the discharge ports where the jet discharge momentum governs the mixing of ambient water ' induced by the discharge momentum with the heated effluent is called the nearfield reg ion. The region of the thermal plume at a distance from the discharge point where the jet induced momentum is dissipated, is called the farfield region. He thermal plume drif ts with the ambient currents in the farfield region whereas in the nearfield region the discharge momentum predominates. Temperature reduction of the thermal ef fluent in the nearfield is accomplished primarily by mixing with ambient water and is therefore extremely rapid. Heat loss in the farfield is accomplished by radiation and convection to the atmosphere and is dependent on surface wind conditions and the dif ference between the natural equilibrium temperature of the water surface and the artificial surface temperature caused by the heated discharge. Temperature reduction in the farfield is governed by ambient processes and occurs over a longer time period than in the nearfield. The fundanental design criteria for the dif fuser is to achieve thermal plume conditions which have an acceptable environmental fanpact and which are consistent with applicable regulatory requirements. Receiving waters at the site are thermally stratified during the summer with temperature differences between surface and bottom ranging from 5 to 80F (Raytheon,1975). Except in the nearfield jet mixing region, the diffuser discharge has no significant effect p on ambient thermal stratification. He impact of the discharge on ambient flow patterns in the vicinity of the dif fuser is evident in the nearfield dif fuser mixing ' zone. We diffuser discharge is expected to have an insignificant influence on the flow patterns outside the mixing zone and no influence in the farfield.
- G.3-6 i
__ 4._,_,,_.._.___,
}
NEP 1&2 ( Discharged water jetting from the diffuser at an initial velocity of about 18 fpe entrains substantial quantities of ambient receiving water. This initial veloc'ity is reduced quickly as the ambient water mixes with the discharge Jets. Within a distance of 250 to 400 feet from the dif fuser nozzles, ambient water is entrained at a ratio of 6 to 1 and the discharge temperature rise is reduced to one-sixth of its original value. It usually takes about one to two minutes for water to reach the surface and undergo a temperature reduction f rom 3 70F to less than 60F above ambien t. Nearfield temperature rises as well as vertical temperature rise profiles as predicted by the physical model are shown in Figures G.3 2-2 through G.3 2-5. Table G. 3.2-1 gives the predicted surface maximum temperature rise as well as the volumes of water occupied by various isotherms at different stages of the tide. Figure G. 3. 2-6 shows the variation of surface area with tidal current throughout the tidal cycle. Additional information on the nearfield temperature rises for the proposed NEP 1 & 2 dif fuser system is given in Brocard (1977). Figures G.3.2-7 through G.3.2-10 show the thermal plume configurations at various stages of the tide cycle for isothermal conditions typical of fall and winter. During spring and summer when the ambient water is stratified, these thermal plume areas are somewhat reduced . It is obvious from these figures that the thermal plume varies substantially in time and space. Table G.3.2-2 gives time-temperature relationships as well as surface areas and volumes for various temperature ' rises and stages of the tide. Additional information on the thermal plume is given in Brocard and Hsu (1978) . Farfield thermal modeling .as well as dye study results indicate that the background ta-arature rise due to the discharge of heat from NEP 1&2 will be less than 0.50 F (Brocard and Hsu, 1978). Brocard and Hsu also found that the temperature rise in g Ninigret Pond due to a temperature increase in Block Island Sound was equal to G.3-7 - _ _ - _ . - - _ _ . - __ , . ~ _ _ , _ _ _ _ _ _ _ . . _ _ _ . __ _. - _ _ _ . _ _ _ _ _ _ _ . _
NEP 1&2 approximately 0 3 times the Block Island temperature rise. These studies indicate that the thermal impact of NEP 1&2 on Ninig ret Pond will be less than 0.2"F. Bottom temperature rises have been extrapolated from both the physical model results. These results indicate that the maximum bottom temperature rise is about 60F above ambien t. R e area of this 60F temperature rise isotherm is conservatively estimated to be less than 2 acres. 3.3 Biofouling Control To maintain the cooling system in an operational condition, it is necessary to control biofouling . The intake portions of the circulating water and service water systems from the intakes to the condensers and heat exchangers are subject to the settlement and growth of marine fouling organisms. These organisn.s, which travel in the water, ( must not be allowed to accumulate on the cooling water system surfaces. Growth of attached marine organisms progressively impedes flow, eventually reaching a point where adequate cooling water cannot be obtained by the pumping system. Mechanical damage to equipment and inefficient or lost electricity production can result if fouling organisns grow to adult stages in the system. The discharge sections of the circulating water system, downstream of the condensers, are not subject to marine biofouling because the normal discharge temperature is high enough to preclude settlement and growth of
' fouling organisms.
From the offshore intakes to the intake transition structure adjacent to the pumphouse, biofouling control is accomplished by backflushing, that is, periodically reversing the cooling water flow in thefintake and discharge tunnels. The backflushing mode of
, operation is used to direct heated watet into the intake tunnel aod thermally shock
( any organisms which might have settled and grown in the tunnel. Backflushing of the system for biofouling control is accomplished by redirecting circulating water flow G.3-8
NEP 162
,within the plant. I For backflushing to be ef fective, a temperature of about 120"F must be reached and maintained at all points in the intake system for a period of approximately 2 hours.
To achieve the required discharge temperature, some of the cooling water is recirculated through the condenser. The total time for the entire backflush cycle including flow reversal and heat treatment is approximately 6 hours, but the 120 F discharge temperature will only be maintained for approximately 2 hours. Backflushing heat treatment is expected to be required about once every 2 weeks during the warmer months of April to November and less frequently during other months. As a result, backflushing will account for less than 2 percent of the plant operating time. Figures G.3.3-1, G.3.3-2 and G.3 3-3 show the backflush thermal plumes during summer conditions as predicted by the physical model. Results for other tidal stages and ambien t temperatures are presented by Brocard (1977). ( Provisions are also being made to permit chlorination of the of fsite intake tunnel from the offshore intake structures to the plant. Chlorination of the intake tunnel will be done in accordance with applicable EPA effluent limitations. Control of marine fouling in the circulating water pumphouse and onsite pipes, the condensers and service water system is accomplished by a combination of chlorination, mechanical cleaning and the application of protective anti-fouling coatings. The pumphouse is divided by a concrete partition into two sections, one for each unit. Each half contains three circulating water pumps, traveling screens, screenwel'Is and one forebay. During a ncheduled shutdown of one of the NEP units, its half of the ptmphouse is isolated from the intake transition structure by closing appropriate valves. t This permits devatering 8f one side of the pumphouse to allow mechanical cleaning of the fouled surfaces. Af ter the pumphouse surfaces have been scraped, they are prepared G.3-9 ~ . . . _
NEP 1&2 and covered with a protective coating oudh as 'a commercially available ~ anti-fouling marine paint. 3.4 Chemical Discharges Chemical discharges to Block Island Sound through the dif f user system will include chlorine used for biofouling control, regeneration wastes from the demineralizers, steam generator blowdown as well as chemicals f rom the pipe cleaning prior to startup. Biofouling control in the pumphouse and onsite intake pipes is accomplished by intermittent chlorination and the application of an anti-fouling coating. The active chlorine is provided by the injection of sodium hypochlorite at feed points in the intake system._ The chlorine discourages the settlement and growth of mussels and barnacles. Accumulation of these organisms could limit the circulating water flow by increasing ( the ef fective roughness of the pipes and'if allowed to grow too large, could also plug condenser tubes af ter detachment from the pipe surfaces. The chlorination treatment adheres to the EPA Ef fluent Guidelines. Chlorine is injected for a maximum of two hours per day on each unit. The dosage is adjusted to restrict the average level of the free residual chlorine at the discharge to 0.2 mg/l over the allowable two hour period (maximum 0.5 mg/1); the Gred rate will depend on the chlorine demand of the water. The free residual chlorine decays rapidly from the point of inj ection to the ocean discharge point for two rtrasons: (a) continuing consumption of this available chlorine with the extended contact time and (b) increased rate of consumption with the higher reaction temperature. In the discharge tunnel the presence of chlorine (even at the reduced . concentration) will supplement the ef fe.ct of the heated water in preventing growth of fouling organisms. G.3-10
NEP 1&2-
, The chlorine injected at the pumphouse also prevents the accumulation of slime in the (
condenser tubes. Whereas the control of marine growth in the tunnels is required
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essentia11y only during the warmer months, the control of slime is required all year rotssd. Herefore, the chlorine is injected throughout the year. If slime were allowed to grow in the condenser, the heat transfer characteristics could be reduced to unacceptable levels and plant output could be significantly reduced. If necessary for effective slime . control, a booster dose of chlorine may be injected just upstream of the condensers. - However, this will not result in discharge chlorine levels in excess of allowable EPA guidelines. Biofouling is controlled in the service water system by continuous chlorination. To accomplish this sodium hypochlorite is continuously injected in the service water pumphouse. It is impossible to dewater and paint the inside surfaces of the service water piping because it is of relatively small diameter and inaccessible. Continuous chlorination, however, is known to be effective for biofouling control and consequently is proposed for the service water system. Water for the plant makeup system is supplied from wells on the site. He well water is treated as required to produce a suitable quality for drinking and demineralizer feed. The feedwater passes through a vacuum deaerator and two parallel strings of demineralizer trains. Each demineralizer train consists of a strong acid (cation) exchanger, a strong base (anion) exchanger and a mixed bed exchanger. He treated water is then delivered to the condensate and primary water storage tanks. Each de.eineraliser. train has a capacity of 240,000 gallons per day (20 hours in service, 4 hours regenerating). During normal operation, one desineralizer train can supply normal plant makeup requirements. He regeneration wastes consist of the ions removed from the process water plus the excesses of sodium hydroxide and sulfuric acid used in , regeneration. Any excess acidity or alkalinity is ' neutralized to a pH range of 6.5 C.3-11
NEP 1&2 to 8.0 by adding caustic or acid as required. Af ter the local pH adjustment, the batch of waste is pumped into the circulating water discharge. A regeneration waste batch of about 30,000 gallons occurs approximately every 3 5 days. The dissolved solids content is approximately 5000 ppm .and consists mainly of sodium sulphate with minor amounts of the other constituents normally found in ground and surface wate rs, such as calcitsa, magnesitsa, sodium, bicarbonate, sulfate, chloride and silica. Upon dilution in the circulating water discharge, the dissolved solids will be reduced to less than 1 ppm.
.The steam generator blowdown system is designed to operate continuously at a variable flow rate which is dependent upon the concentration of solids in the steam generators.
The blowdown processing system is sized to maintain the total solids concentration in the liquid phase of the steam generators at 125 ppm or less for design conditions. ( The normal blowdown rate is approximately 5 gpm per steam generator. The maximum continuous design blowdown rate is approximately 100 gpm per steam generator. This blowdown stream is added to the circulating water system discharge and undergoes a dilution of about 20,000 to 1. The blowdown stream contains ammonia, chloride, copper, flouride, hydrazine, iron, lead and silica. The concentration of each of these chemicals in the blowdown is less than 1 ppm and in the circulating water discharge, less than 0.00005 ppm. . The coolant, steam and condensate piping systems will be cleaned before startup to remove debris and any oily film. This involves flushing with detonized water before and af ter flushing with a hot alkaline solution. When the alkaline solution is displaced, it is treated by passage through the holdup tank and pli adjustment tank before being discharged to, the ocean via the circulating water system. G.3-12
NEP 1&2 35 Coolina Water System construction Techniques (
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Construction methods and procedures are not finalized at this time. .An extensive geotechnical exploration program of the offshore bedrock and overburden deposits alcug the tunnel routes and at the locations of the offshore intake and discharge structures will be conducted in order to verify the feasibility of the concepts discussed below. The exact location and depth of the tunnels together with their associated of fshore ctructures and the methods by which they would be constructed will be established cubsequen t to this program. The construction of the tunne.s through the rock will be accomplished by conventional methods (drilling and blasting) or by using a tunnel boring machine; both methods working from the plant site. Dewatering ef fluent from the tenneling operation will be processed for separation of any contaminants such as oils, diesel fuels, etc. The processed water will then be pumped to a settling basin as described in Applicant's a'pplication for ( o NPDES permit. Offshore vertical .shaf ts will connect the deep bedrock tunnels to the intake structures cnd discharge diffuser. These shaf ts may be constructed from a floating vessel commonly referred to as a jack-up barge. The jack-up barge will be positioned over the location of the shaf t, and a steel casing then driven through the overburden deposits. Once
- the casing is firmly seated on bedrock, the overburden within the casing will be removed, cnd a large rock roller bit drill will be used to drill downward through the bedrock.
A cylindrical steel shaf t with a concrete lining will then be installed in the casing and anchored to the bedrock with concrete grout. The steel shaf t will contain diaphragm covers and valves' to ensure that the ' ocean water does 'not enter the shaf t' or tunnels until the appropriate time in the construction sequence. The completed steel- shaf ts k will support the three intake structures and also provide a transition between the discharge tunnel and the pipe discharge dif fuser. Haterial excavated from within the G. 3-13 e- me aa.==4..w
.e e
NEP 1&2 l casings, estimated not to exceed 3000 cubic yards, will be deposited on the sea bed adjacent to the excavation. A typical intake structure is shown on Figure G.3.1-1. The intakes will be constructed of reinforced, precast concrete or metal and barged or towed offshore for installation, or constructed in the dry utilizing steel cof ferdams. Little, if any, environmental impact is associated with the operation. Figure G.3.2-1 is a schematic view of the multiport discharge dif fuser through which the cooling water will be discharged. The diffuser pipes will be buried under the ocean bottom aa shown, and will be installed subaqueously in an open cut excavation. Clamshell or bucket dredging will be used to remove the sediment from the dif fuser pipe excavation. The total amount of sediment to be removed is approximately 122,000 cubic yards (includes 3000 cubic yards removed from the riser shaf ts), and will be -placed [ alongside the trench. The dif fuser pipes will be supported by approximately 14,000 cubic yards of clean bedding material. It is anticipated that the excavated material will be suitable for use as backfill and subsequently up to approximately 94,600 cubic yards'will be placed back in the trench af ter the dif fuser pipes are installed in the trench. The excess material will be naturally distributed over the affected area such that the final bottom contours will not change significantly f rom original conditions. The fLnal decision on the suitability of the material for backfilling will be determined from test borings, for which a Corps of Engineers permit has been received (Permit No. R1-QUON-78-16 7) . If. the excavated material is not suitable for use as backfill, it will be disposed of at an approved location. k C.3-14 .
NEP 1&2 An alternate construction method will be considered should the boring program determine I that geological conditions are suitable. De bedrock tunnels would be extended the . cntire 1200 foot length of the diffuser. He dif fuser nozzles would be installed utilizing a drilled-in concept, .whereby diffuser nozzles are directly connected to the bedrock tunnel via individual riser shafts of appropriate size. C ( G.3-15
1 . 2 NEP L&2 i
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4.0 BI0IDGICAL EFFECTS OF THE PROIDSED COOLING WATER SYSTEMS ON REPRESENTATIVE'IMPORTANT l SPECIES ' i 4 4.1 Methodology i Impacts on the aquatic environment which are associated with anypower plant may be divided into two broad categories: (1) short term impacts associated with construction ! of the facility, and (2) impacts ditch result from the long term operation of the cooling water system throughout the plant's life. We methods utilized to evaluate these two u . areas of impact are addressed separately below in Section 4.1.2. he represen ta tive important species' concept was used to evaluate the significance of these categories j of impact. We basis for the selection of these species is discussed in Section 4.1.1 i in this document. 1 i ( 4.1.1 Re p r ese n ta tiv e Important Species and the Rationale for their Selection A he Representative Important Species (RIS) list presented in Table G.4.1-1 was selected by the Region I Administrator of the United States Environmental Protection Agency in accordance with the regulations of 40CFR, Pa r t 122. > i 4.1.1.1 Basis for Selection of Species l The selection of representative species for this discussion is based upon site specific 1 information on the population characteristics of permanent and transient species, and [ the experience gained on the environmental ef fects of powe r plant construction and operation upon aquatic biota at 6ther power plant sites. We specific criteria typically used for selectity, representative species are: i I i i 1 ' !, G.4-1
- x. - m.m a n- -
--v w ~++x_ _~---=__ - - - -
.?:- w ===-. --- ~ m
- . . - .~
l NEP 1&2 1 (
- a. Threatened or endangered status
- b. Nuisance
- c. Commercial or recreational importance, and
- d. Dominance.
The species which have been selected are representative of the trop *.ic levels in the community and the major habitat types, as well as the permament sad seasonal residents-found within the surrounding environment. The representative species thus provide the reference points by which the general condition of the balanced indigenous community can be assessed and the b iological in teg rity o f t he wa te r de te rmined. A large number of species have been collected in the surveys conducted in th.: Block Island Sound /Ninigret Pond complex. Although all species 'are considered in the r election ! of representative species, only those species that meet the criteria listed above in Section 4.1.1 were selected. . Dominant species of phytoplankton and zooplankton were not included und er the representative species category in this demonstration for several reasons. Commonly, the lower trophic levels of natural " balanced" ecosystems are characterized by wide fluctuations in population size and biomass. These fluctuations are due to a combination of factors, including density dependent mechanisms such as selective or non-selective predation and . density independent mechanisms such as daily or seasonal changes in natural conditions. These extreme fluctuations lead to difficulties in data collection and analysis, and makes the use of the af fected populations as indicators of minor enviornmental modifications inapproprite. In addition, short reproductive cycles and i rapid regeneration of most planktonic organisms lessen any power station impact on this component of the ecosystem when compared to longer lived aquatic species. Finally, G.4-2
NEP 1&2 ( power station induced mortality of lower trophic level organis.ms does not negate their contribution to the ecosystem as sources of nutrients and detritus. he representative species selected by EPA are listed in Table' G.4.1-1. We following i discussion provides a rationale for their selection. l 4.1.1.2 ' Threatened and/or Endangered Species No threatened or endangered species have been identified within the study area. 4.1.1.3 Nuisance The only potentially significant nuisance taxa identified within the study area was , the dinoflagellate genus Gonyaulax. Stone and Webster (1975) reported that there has been no observed increase in the incidence of Gonyaulax spp. as a result of the operation of Pilgrim Nuclear Power Station, and Prakash (1967) found that temperature was not I as important as salinity in controlling the summer abundance of Conyaulax tamarensis. Pt)reover, the volume of water af fected by a thermal increase in excess of 1.5"F is small compared to the flux of ambient water passing the discharge area and an artificially induced red tide is not likely. 4.1.1.4 Commercially or Recreationally Important The discussion and tables in Section 2.2 of this appendix indicate that the following species provide a reasonably or potentially important component of the commercial fishery either directly as part of the catch (C) or indirectly via the planktonic life stage (P) or are important to the sport fishery (R): G.4-3
-_--__._______________.____________.___,..___.__._____.________,_,_,____.._.__________._._______.___t_
NEP 1&2 I s Atlantic menhaden C, P Red hake C Atlantic herring C Little skate C Scup C Lobster C Atlantic mackerel P Squid C Butterfish C Hahogany-quahog C Summer flounder (fluke) C Surf clam C Windowpane C Oyster C , Winter flounder C,P,R Bay scallop C Atlantic cod C Hard clam C Silver hake (whiting) C Soft clam C Striped bass R Bluefish R (, Two of the above commercial species (mackerel and winter flounder) have significant larval denisites in Block Island Sound. While larvae of the others may be present, their low densities suggest that the study area is not near a' major spawning or nursery area. Therefore, species selected for the representative commercial species are those which have the highest potential for a power plant induced impact plus those species representative of ' ecological roles within the community. The selected species of the commercial and recreational fishery are: Atlantic menhaden, scup, Atlantic mackerel, butterfish, winter flounder, silve r hake, lobster, s ,q u i d , and hard clan. The adults of many of the other species exist in relatively low numbers in the area of the proposed . intake and discharge. Pbrthermore, many of the adults of these species either are not subject to entrapment and significant thermal plume contact (e.g., surf . clas, bay scallop and sof t clam) or are represented in this discussion by a behaviorally ( similar member of their taxonomic family (e.g., summer flounder, windowpane, Atlantic
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C.4-4
NEP 162 cod and red hake) . Among the area's most impo r tan t recreational species are the winter flounder, striped bass and bluefish. These three species have all been included as representative species. 4.1.1.5 Dominance It is appropriate in considering the representative species in an area to include dominant forage species and habitat formers which may be necessary fo r ecological stability. These species are (1) the cunner, which is the second most abundant ichthyoplankter (behind mackerel), (2) the bay anchovy whose larvae were the third most abundant, (3) the blue mussel which is dominant in the meroplankton of Block Island Sound, (4) eclgrass (Zostera marina) which is abundant in Ninigret Pond, (5) the sand lance (Ammodytes americanus) and (6) sand shrimp (Crangon septemspinosa) which are both important larval contributors to the plankton. ( 4.1.2 Methods of Impact Analysis 4.1.2.1 Tha Impacts of Construction In add ressing the impacts associated with construction of the cooling wa ter system, Applicant has related various ecological parameters associated with the representative species to the temporary environmental disturbances which will be present during construction of intake and discharge structures in Block luland Sound. Construction and installation of the circulating water system tunnels will have no ef fect on Nini retd Pond. During the construction of of fshore riser si sf ts and installation of the dif fuser and intakes in Block Island Sound, there will be a temporary increase in siltation and turbidity of the water. There will also be disruption and removal of bottom habitat within the immediate area of this construction. While increases in siltation and water turbidity can af f ect aqua tic biota, not all C.4-5
NEP 1&2 I opecies are equally susceptible nor are all kinds of suspensoids equally harmf ul. increased turbidity can cause a reduction in the abundance and photosynthetic rate of 4 phytoplankton (Emery and Stevenson,1957; Bartsch,1960; Copeland and Dickens,1969). reduc tion The reduction in photosynthetic rate is proportional to the amount of light in the water column due to turbidity. Flocculation and aggregation of tempo rary suspensoids can also mechanically trap phytoplankton and carry the cells to the bottom (Brehmer,1965; Gunnerson and Emergy,1962). Some zooplankton may also be adversely af fected by turbidity by the reduction in primary production. Siltation can be detrimental to benthic biota by burying or blanketing these organisms with sediment, which, if excessive, could cause their mortality by asphyxiation, and by depressing feeding, growth, and egg and larval development r stes (Emery and Stevenson, 1957; Brehmer,1965; Davis,1960; Dodgen and Baughman 1949; Loosanotf, 1961). Salla et al. (1968), however, have observed in the laboratory that at least one benthic species , { (i.e., adult lobsters) can tolerate concentrations of suspended matertai as great or greater than those resulting from dredge spoil dumping with no adverse ef fects. Turbidity can .also af fect finfish. At his,h turbidity concentrations, ingle et al. (1958) found that several estuarine fishes suf fered morality probably due to suf focation brought about by clogging of the opercular cavities and damage to respiratory structures. Resistance to disease, reproduction, and behavior of finfish can also be af fected by increased turbidity (EIFAC, 1964). To the contrary, Flemer et al. (1967) could find no alteration in the abundance and distribution of striped bass, winter. flounder silversides and menhaden larvae and others due to tuspended and deposited sedimen ts during dredging and overboard shallow spoil disposi.1 operations in the Upper Chesapeake Bay. Fur thermore, Ingle et al. (1955) have neced that some fish species exhibit an avoidance reaction to increasing turbidity tevels, thereby preventing movement into a potentially adverse environment. There will be no intake and dincharge cons'truction G.4-6 J
l
. . j NEP 1&2 :
i l related .ef fects in Ninigret Pond. Factors considered include' (1) tempo ral and ' spatial distribution of the various life stages, (2) mobility, (3) behavioral characteristics, and (4) feeding habits. Because tunnels will be utilized for the cooling water sistem, construction related impacts will be limited to those associated with installing the intakes and dif fusers in Block Island Sound. In Block Island Sound, the disruption and removal of bottom sediment in the immediate construction area during installation of the circulating water system will primarily af fect benthic biota. Bottom sediment disruption will temporarily interfere with the area's usage as habitat 6hile organisms associated with sediment removed during dredging may be destroyed. However, no permanent detrimental benthic impact from circulating water system construction is anticipated. The system will be located in areas of relatively low benthic population density. Furthermore, benthic species in the proposed construction area are found throughout the region, and upon completion of construction, the environs disrupted are expected to be recolonized and should readily return to their pre-construction state. 4.1.2.2 The Impacts of Operation Impacts associated with the operation of the cooling water system of a power plant may be divided into three distinctly different areas: (1) the entrapment or impingement of nekton, (2) the entrainment of and subsequent in-plant ef fects on planktonic organisms, and (3) the ef fects of the thermal plume once it is released f rom the plant. In this document, each of the areas is considered separat'ely and the cumulative ef fects are then addressed. En trapmen t/Impingemen t. Entrapment is characterized by the drawing in of free swimming aquatic organisms into the cooling water system. Impingement occurs dien entrapped i organisms larger than three-eighths of an inch are ultimately prevented f rom passing G.4-7
NEP 1&2 through the traveling scre'en barrier. Organisms which f all into this category are ( usually fish and occasionally invertebrates such as crabs and lobsters. Fish return systems are not considered practical for NEP 1 and 2 (see ER Section 1010). Iloweve r, Applicant is proposing both an advanced of fshore intake design (velocity cap) and a location which minimizes the potential for entrapment. Therefore, an important consideration in evaluating the itspact is whether or not the potential for entrapment and impingement is environmentally acceptable. Constraints on the location of the intake are discussed in Section 5.0 of this document and include the requirement for sufficient water depth to prevent exposure of the structure during storm conditions and its positioning close enough to shore to minimize the potential l for interference with commercial fishermen. The potential for entrapment and the l resultant impact is dependent on several operatior.a1 and environmental variables. From an operational standpoint, the design, location ami capacity of the intake determine ( its entrapment potential. Environmentally, f actors such as the particular species involved, their age, size, swimming speed, behavior, temporal and spatial abundance when associated with physical facto'rs such as water temperature are also taken into consideration. While of fshore velocity cap intakes have been installed and are said to be ef fective f in reduc ing the en trapa'en t and ultimate impingement of marine fishes and macroinvertebrates (see ER Section 5.1.4.2) at electric generating stations in California and Florida, this type of intake design has not been utilized in coastal New England waters. It is, therefore, dif ficult to predict (based on regional' operational data) the effect of NEP 1 & 2 on the entrapment and subsequent impingement of indigenous fish species. ( The potential ef fects of the proposed NEP 1 & 2 intake system were, however, based on a camparative study of the performance of extant coastal velocity cap intakes hy Coastal C.4-8
; i- .
i
- NEP 162 f'
- f Zone. Consultants (1979). his study examined the operational velocity cap intakes in southern California and Florida with respect to design criteria, operational conditions and the faunas exposed to them. 'Ihe NEP 1 & 2 Representative important Species we re-a paired with ecologically similar species occurring in Florida and/or southern California.
'Ihe life histories of the paired species were examined in detail, and the entrapment records of the California and Florida equivalent species were studied. From this information, estimates of the relative entrapment potential for the NEP 1 & 2.RIS were prepared.
During backflushing, water will be recirculated through the condensers in order to provide the 120 F nece'ssary to kill biofouling organisms, primarily mussels, in the in take tunnel. As a result of recirculation flow, the volume of cooling water drawn in and discharged will be reduced f rom the normal flow. The reduc tion in wa ter utilization is a constant 50% of the normal circulating water flow requirements provided cool service water is available from the unit not being backflushed. Under these conditions, entrainment mortality during backflushing also will be reduced by 50% as a result of the reduced flow requirement. Despite the reduction in water consumption, it is anticipated that the rate of entrapment of finfish will increase dur ing backflushing as a result of the high intake velocity th ough the dif fuser nozzles and the absence of a velocity cap. Because of the relatively short time involved, however, the increased entrapment mortality is not judged to be important. Ef fects in the Discharge Plume. Temperature is among the most influential ecological mediators of biological systems af fecting a poikilotherm's temporal and spatial distribution, as well as their metabolism and behavior. Although mammals and birds have partially solved the problem of temperature directed ef fects by their ' internal compensatory maintenance of a nearly constant body temperature (i.e., homothermic 4 condition), other taxonomic groups experience relatively great variation in their G.4-9 i l i
- l
NEP 1&2 internal temperature in conformance to the temperature of their surrounding environment ( (i.e., poikilothermic condition) . Of course, poikilotherms have undergone considerable adaptation to the varying temperatures of their particular environment and are generally capable of withstanding most naturally encountered temperature fluc t ua tions . Within tolerable temperature ranges, there are great dif ferences in the rates of biochemically based metabolic processes which can influence such things as an organism's development, maintenance, growth, reproduction and behavior. Naturally occurring background temperatures vary temporally (diurnal and seasonal) and spatially. Ambient tenperature fluctuations may be extremely <., mall in deep ocean waters whereas, nearshore water temperatures can vary by several degrees, daily as well as seasonally. As discussed earlier in Section 2.~1, the temperature in Block Island Sound typically ranges from 34 F in the winter to 700F in the summer. Diurnal and semi-diurnal temper?ature fluctuations of 2 to 3 F are typical of the area. In the spring and summer ( The _ a vertical thermal stratification of as much as 60F exists in the water column. rest of the year the water column is nearly isothermal. While a species has evolved the ability to survive ambient temperature fluctuations, there are both upper and lower temperatures and temperature fluctuations beyond which active life can only exist for a short time period. Within temperature tolerance ranges, the degree of activity is again governed by the temperature. Thus, temperature limits that range for existence and governs the capacity tc be active within tha t range. The discharge of waste heat .to the aquatic environment may have a bearing .upon such normal activiti.es described above. What degree there will or will not be an impact will have to' be determined by an evaluation of all variables that . enter 'into the ' organim/ water temperature interface. In order for one 'to predict the ecological af fects . ( of aquatic waste heat disposal, one must know: (1) the location, quantity, and water temperature of the circulating water discharge, (2) the af fect of the discharge on the G.4-10
~
NEP 1&2 natural thermal state.of the receiving water body, and (3) the ability ot~ the organism to tolerate such a change ab ove no rma l background temperature levels. A description of the NEP 1 and 2 heat dissipation system is given .in Section 3.4 of the Environnental Report and Section 3 0 of this document. At full load and rated flow, the cooling water temperature will be raised approximately 370F as it passes through the condenser. Transit time between the condenser and ~ the point of discharge is estimated to be 14.5 minutes. Cooling water is discharged into the Atlantic Ocean by means of a submerged multiport diffuser. As a result of the hydrodynamic characteristics of the heated discharge it is expected the plume will have some contact with the sea floor before it ascends to l the surface. Based on analytical predictions presented in Section 3.2, approximately two acres of the ocean bottom could experience, at most, a maximum induced temperature ( increase of 60F. Due to the rather nominal rise in temperature that an organism might experience and to the comparatively small size of the bottom area contacted, no appreciable impact is anticipa ted however. Heated water will exit the diffuser ports at an initial velocity of 18 f ps. This initial velocity will be raiuced quickly, however, as the ambient water mixes with the discharge
.j e ts. Within 250-400 feet of the dif fuser nozzles, ambient water will be entrained at a ratio of 6 to 1 causing a corresponding reduction in the temperature rise of the heated water to approximately one-sixth of its initial discharge value. It will take only a few minutes for the discharge water to reach the surf ace and for the water temperature to be attenuated to approximately 6 F above ambient.
Generally the surface plume temperature rise isotherms, areas and location vary as a function of tidal current and phase. As indicated in Section 3.2, changes in tidal ( , current significantly af fect the-thermal plume characteristics. Results from a C.4-11
NEP 1&2 hydrothermal physical model study (Table G. 3.2-1 and Figure G.3 2-6) indicate that the I surface maximum temperature rise, which occurs at slack tide, is about 6 F and occupies less than 1 ac re. As indicated in Table G.3.2-1 once the tidal current is above 0.5 fps the maximum surface temperature rise is less than 5 F. Having reached the surf ace, a plume flow away zone 1s created and the remaining jet momentum is dissipated by entraining additional water'. Beyond this region temperature decay of the thermal plume oc(urs primarily by diffusion and by surface heat loss to the atmosphere. Both of these n atural processes is slow and requires a variable amount of additional time to reach ambien temperature conditions. From the standpoint of plant oreration, marine organisms will be subjected to thermal effects either (1) by being entrained and passed through the cooling water systems where they will experience the full temperature dif ferential of 37 F on the discharge side of the condenser, or (2) by being entrained in or interacting with the heated plume C once it is discharged. In order to reduce the number of organisms entrained, Applicant has selected a low volume of cooling water flow and the resultant high temperature increase of 37 F. While the low flow will reduce entrainment, the high temperature increase is expected to cause almost complete mortality of those organisms tha t are entrained; this is considered preferable to the alternative of a cooling system with higher flow and lower temperature rise. Regardless of the cooling systems temperature rise, it is expected that a substantial mortality of entrained organisms will occur as a result of mechanical and hydraulic stresses. Th e r e f o re , to minimize overall entrainment mortality, it is considered necessary to minimize the cooling water flow.
'lhis is accomplished by selecting a cooling sys tem with a high temperature rise.
In contrast to the foregoing, aquatic organisms may encounter short term or localized temperature stresses within the thermal plume of the station's cooling wa ter sys tem i discharge. Here there may F + a temperature maximum greater than those naturally present G.4-12
NEP 162 N,. Nt e Zt where: , N, = number of larval sand shrimp at hatching Nt = number of larval sand shrimp at time t Z = instantaneous mortality rate (0.0967/ day) t = time in days Based on an estimated average density of larval sand shrimp at hatching, and assuming 100% plant load, an equivalent'of 6.387 x 10 9 Stage I sand shrimp would have been entrained in 1978. To determine the number of adults that would have been lost through entrainment of these larvae, the following assumption was made. If the population is in equilibrium, the fecundity of a female will be reduced to two breeding adults in ( one generation or. J S = 2/F where: , S = survival'from egg to adult, and F = fecundity of a breeding pair during their life. Survival from egg to adult is a product of survivorship f rom egg to larvae and larvae
. ~
to ad'ul t . For conservatism survivorship from egg to larvae was assumed to be l'0 0 % .
'liaefner (19.76) provided a fecundity relationship of Y = 2 611 + 0. 00 7 7 .(X-15 6516 )
where 7.- C. 4-113
NEP 1&2 Y = number of eggs per female . ., X = cubed length in mm. { lic found egg bearing females ranging in size from 16-70 mm. Smith (1950) never found edult sand shrimp greater than 30 mm. Beach seine data from Ninigret Pond f o r 19 78 showed that 76% of adult Crangon were less than 40 mm (YAEC,1979). Using a mean length of 30 mm for ovigerous females a fecundity of 1614 eggs per female was calculated.'
'Ihis provided a survivorship f rom hatching to adult of 0124%.
Based on estimates generated by Applicant, the projected entrainment of larval sand 6 chrimp, at hatching would result in the loss of 7.92 x 10 adults. The weight of these adults lost due to entrainment was estimated from the length-weight relationship provided by Wilcox and Jeffries (1973). . Log W = 0.040L + 1'.0 where: W = weight (mg) L = Length (mm) Based on Applicant's estimate, the projected loss of adult ' shrimp would weigh 1.256 x 10 6g ~(2763 lbs). Salth (1950) estimated the ' standing stocks of E septemspinosa in Block Island at 0.239 g/m2 . Assuming an area of 400 sq mi, the estimated loss of adult shrimp represent 0.5%
- cf the standing. stock of sand shrimp in Block Island Nund in 1949 Smith also estimated that fish corisumed 5.5g of ~ food /g of fish / year *and that sand shrimp t
comprised 7 2% of the stomach contents of fish. Therefore the' amount of adult C. G.4-ll4 . u
NEP 1&2 profile. Since all the representative species (except celgrass) are poikilotherms (cold blooded), temperature is an integral factor in their presence or absence at the site. In order to identif y the correlation between the presence or absence of a specie s wi th temperature, the relative temporal abundance of eggs, larvae, and adults found at Station BIS-A -(Figure G. 2.2-1) , which is the most representative of the discharge location, is plotted below each temperature profile. It should be pointed out that these temporal abundance profiles are relative only within a particular life stage and, the re fo re, one should not compare the relative size of one life history stage with another. The number in the largest block represents either the number of organisms /100 cubic meters during the period of greatest abundance of eggs and larvae or the number of adult individuals captur ed dur ing four otter trawls toys f o r any one month. ( The last data input parameters are the temperature tolerance values derived f rom the literature. This information is presented in one of three ways:
- a. A specific temperature related event (e.g., upper lethal limit, incipient lethal temperature, avoidance response temperature, temperature preferenda, etc.) based on a particular acclimation temperature;
- b. A specific temperature related event where no correspondlng acclimation value was provided; or
- c. General background temperature information, such as the organisms's spawning temperature, preferred temperature, growch temperature, etc.
Where acclimation temperatures are provided, a specific temperature event is plotted by relating the acclimation value to a natural'1y occurring surf ace water temperature 4 found at the NALF site. An example is provided (Figure G.4.1-1) for an adult with an G.4-15
NEP 1&2 upper lethal temperature limit of 770F based on an acclimation temperature of 58 F. ( Commencing at Point A (58 F), a horizontal line is extended f rom the organism's given acclimation temperature to a location on the temperature profile which corresponds to that date when such a temperature was observed at the NALF site (Point B). A perpendicular line is then drawn up to that temperature found by the author to be the animal's upper lethal temperature limit (Point C) . In some cases, the actual test acclimation temperature is higher than the average maximum surface temperature observed at the site (i.e., 700F in August) . In order to denote such an occurrence, the acclimation temperature is placed in parentheses (Point D) and a dashed vertical line is drawn to its corresponding temperature related event (Point E). For this example, the author acclimated the organism at 770F and found it has an upper temperature tolerance of 880F. ( In those instances diere no acclimation temperatures are provided for a given temperature related event, or where information such as spawning temperature, optimal growth values, etc., are given, the various values are plotted on the right hand side of the figure. In this example, an upper lethal temperature for larvae was observed at 74 F whereas a spawning range is given for the species between 56-67 F. Having plotted all such data points a general relationship can then be obtained between the a given species' life history scage, observed temperature tolerance and projected impact with the surface temperature maximum induced by plant operation. Effects Within the Plant. Applicant has designed the cooling water system in such a manner that the cooling ' water flow volume'(hence the number o_f entrained organisms . subject to in aplan't effects) is minimized. In order to achieve this ' low flow, it is necessary to raise the Delta T; at NEP 1 & 2, 370F is the highest practical temperature consistent with engineering and enviramental considerations.
. G. 4-16
NEP 1&2 ; The predicted annual entrainment of eggs and larvae of the representative species is presented in Table G.4.1-2. From this table, it can be seen that the vast majority of total entrainment of ichthyoplankton will be incurred by relatively f ew species. In descending order of abundance, the largest sources of ichthyoplankton were: cunner, Atlantic mackerel, anchovy, and winter flounder. Because of the importance of these species, Applican t commissioned Stone and Webster Engineering Company to model mathematically the entrainment ef fects of power plant operation on the populations of these species (Stone and Webster, 1976). The other selected representative fish species have lower densities than the above four, and, in several cases, their ichthyoplankton are not even present. For these species, available information on the population statistics have been gathered. Depending on the available information, the ef fects of in-plant mortality have been correlated to: s ( (1) the loss of a certain number of females, (2) the projected loss to the adult fishery, and (3) the commercial harvest. In modeling th'e ef fects of entrainment. on several of the s pe cie s , the assumption has been made that if the population is in equilibrium, the fecundity of a female will be reduced to two breeding adults in one generation. This may be represented by the , equation presented in Horst (1975): 2=SxF (1) where: S = survival from egg to adult, and F = the fecundity of a breeding pair during their life. ( Transposing, G. 4-17
NEP 1&2 ( S = 2/F (2) From this consideration, the probability of an egg reaching . adulthood may be calculated. S is also equal to the product of survivorship of the egg to larvae (Se) times survivorship f rom larvae to adult (S t) or, S=S g x S, (3) and St = S/Se = 2/S eF (4) This equation provides a prediction of the probability of a given larvae reaching adult. The number of adults lost as a result of entrainment is predicted by summing the etfects as predicted by multiplying S and Sg times the ' total egg entralignent and the total larvae ( entrainment, respectively. Total Impacts. The total impact section of the seventeen representative species will stummarize the effect of each major factor (i.e., entrapment, entrainment and thermal plume) and assess the aggregate impact on the population. Other sublethal ef fects are
' addressed in Section 4.3.
4.2 Impact Assessment
- 4. 2.1 Atlantic Menhaden (Brevoortia'tyrannus)
- 4. 2.1.1 Life History.
The Atlantic' menhaden. is a' widely distributed' migratory species which is 'found along the entire Atlantic sed aard between 270N and 450N. The majority of the population winter in offshore waters south of' Cape Hatteras and moves northward in early spring G.4-18 i
NEP 1&2 (Nicholson, 1971). They return to southern waters in the fall months, i.e., October-December. The menhaden is one of the most abundant fishes found along the coast. 6 Juvenile and adult menhaden are non-selective plankton feeders. Comb-like gill rakers filter out plankton as the fish swims with its mouth open. Bigelow and Schroeder (1953) repo rted that menhaden spawn at sea and tha t the chief production was south of Cape Cod. While most of the eggs are probably spawned at sea, there is evidence that, in southern New England, significant spawning takes place in large estuaries (Marine Research, Inc., 1974). In New England, spawning may occur f rom May to October (Reintjes, 1969). Investigations by Marine Research, Inc. in areas of Narragansett Bay during 1973 revealed the presence of menhaden eggs in ichthyoplankton collections as early as mid-April, with maximum abundance around mid-June. The eggs are pelagic and usually hatch within 48 hours (Kuntz and Radclif fe, 1917). There is ( no evidence that Ninigret Pond and adjacent wate.rs of Block Island Sound are particularly significant spawning areas for menhaden, although its eggs and larvae were found to occur in both areas during the summers of 1974 and 1975. The temporal abundance of menhaden eggs and larvae (1974-1975) is depicted in Figure G.4.2-1; the spatial abundance is depicted in Figures G.4.2-2 through G.4.2-5. On the average, menhaden weigh approximately one-half pound as one-year-olds and nearly a pound as three-year-olds. The growth rate declines af ter age three. They may enter the fishery, principally along the south Atlantic coast, when less than one year old. The majority become sexually mature in their third year (O'isen and Stevenson, 1975). Menhaden have supported an important commercial fishery f rom Cape . Kennedy, Florida to Cape Ann, Massachusetts, although regional scarcity resulted in no New England landings
. r during the 1%3-1%8 period (01sen ard Stevenson, 1975).
U. S. fishermen catch more pounds of menhaden each year than any other species (Henry G,4-19
NEP 1&2
. e t al. , 1965). Menhaden are not processed for human consumption. They are usually reduced to meal which is rich in protein and which is used as a food supplement in' animal teed. Additionally, the oil derived f rom menhaden is used in paints, soaps, lubricants and a variety of other commercial and industrial products.
Aside from its own commercial value, the menhaden also serves as a principal forage species for such important predators as blu Cish and striped bass. 4.2.1.2 Impacts of Construction. Adult menhaden can be found in the area of the site f rom March until December. Schools of adult menhaden are not only transitory, but are sufficiently mobile to avoid suspended sediments and turbidity. Increases of suspended sediments and turbidity in the immediate area of construction could adversely affect some eggs' and larvae floating through the construction site. However. because the most intensive menhaden . spawning in southern New England takes place .in the large bays and . estuaries, such as Narragansett Bay, few eggs and larvae are present, and the effects of construction on eggs and larvae in Block Island Sound is expected to be very minor. Under these circumstances, no appreciable harm to the Atlantic menhaden populations is anticipated as a result of construction. 4.2.1.3 Impacts of Plant Operation En trapmen t. . Menhaden are of ten impinged on the intake traveling screens of power plants. Along the northeast coast, there have been several instances of substantial intake impingement of menhaden (Young,1974). These impingement cases, however, occurred at facilities with shoreline intakes. Menhaden appear to be vulnerable to entrapment at shoreline intakes. Based on their comparative study, Coastal Zone Cons ~ultants (CZC) (1979) concluded that the entrapment potential for this species at NEP 1 & 2 ranged from medium to high based on the following reasons : (1) Its RIS counterpart, the northern anchovy (Eng raulis
-G.4-20 ,
NEP 1&2 mordax) is entrapped in relatively high numbers by velocity caps in southern California; (2) Atlantic menahden are seasonally present for over 6 months in southern New England. We young-of-the-year should be particularly abundant in October, while the adults -may be abundant throughout the summer; (3) This species is planktivorous and remains in schools at least into early evening. Ilowever, CZC (1979) also identified factors utich may tend to minimize entrapment of menhaden. Rese factors included: (1) Atlantic menhaden are wary; and adults, especially, may avoid the intake structure; (2) The
- young remain in the estuary much of the time and move to the nearshore waters at the onset of migration. (3) Brevoortia tyrannus and B. smithi are both present in the vicinity of the operating velocity cap intake at St. Lucie Generating Station in Florida yet impingement of these species has not been reported.
'The critical swim speed f or menhaden has been reported by Wyllie e t al. (1976).
Utilizing their data, the average critical swim speeds for menhaden of 3 7 to 7.1 inches in length was calculated to be 1.4, 2.3, 2.3, 2 8, and 1.5 f ps at water temperatures of 41, 50, 59, 68-69. 8, and 75. 2-7 7 F, respectively. Thus the potential for menhaden entrapment is not considered a significant problem since the fish generally have a swimming capability greater than the intake velocity of 1.5 f ps. T Since no known regional operating experience on the entrapment rate of menhaden at sthmerged offshore intakes is available, the entrapment mortality of menhaden predicted for two nearby nuclear power stations (i.e., Pilgrim Station and Millstone Station) with shoreline intakes was examined to place any potential menhaden entrapment losses at NEP 1 and 2 in perspective. The significance of predicted menhaden entrapment losses at Pilgrim and Millstone Stations was assessed by population simulation modeling (Stone and Webster,1975; Horst, 1976). 1he estimated number of menhaden which will be annually impinged. on the Pilgrim Station Units 1 and 2 intake screens was estimated to be 18,567 fish (Stone and Webster 1975). G. 4-21
NEP 1&2 ( This annual entrapment of menhaden at Pilgrim Station is expected to cause a reduction in the menhaden population of 0.00073 percent over a 50 year period of plant operation. Since the effect of. menhaden impingement at Pilgrim was negligible, Stone and Webster (1975) concluded that the menhaden population should not be adversely affected. The number of menhaden annually impinged on the in take screens of Millstone Units 1, 2 and 3 was estimated to be 1018 fish (Horst, 1976). The mortality coef ficient derived 4 from the annual impingement loss given above was of such small magnitude (i.e., j 0.0000005) that it was not used by Horst in his population simulation model. Instead, i a greater .than average menhaden mortality incident that occurred at M111stene Unit 1 i was used to derive the intake mortality coef ficient for the simulation model. This i 1 incident occurred in. the fall of 1971 when about 50 million j uvenile menhaden and blueback herring were killed at the Unit 1 intake. Extrapolating the Unit 1 mortality (, to all three Millstone '? nits results in a notable mortality of 210 million fish. The a resulting mortality coef ficient for entrapment losses of this magnitude (used in the population simulation model) is 1,740 times larger than the normally expected in take nortality and represented a worst-case incident. As a result of his analysis, Horst (1976)~ concluded that no detectable change in the population dynamics of the Atlantic i senhaden population would result f rom the ope ra tion of Millstone Sta tion. The analyses discussed above clearly demonstrate that within the range of annual intake-entrapment losses of 1000 fish to 210 million fish, no significant impact occurred to the Atlantic menhaden population. Since any projected annual intake-entrapment loss of menhaden at NEP 1 and 2 would probably fall on the low side of the range. of losses - discussed above, and since the NEP 1 and 2 intake structure incorporates features of 1 design (e.~g., offshore velocity ' cap) diich have proven extremely successful in minimizing l ( \ the entrapment of fish, it is concluded that entrapment of menhaden at the NEP 1 and '
-2 intake should not appreciably harm the Atlan tic menhaden population.
4 ' G.4-22
NEP 1&2 9 Within the Discharge Plume. 'As one might expect f rom a species found in commercial quantities as far south as Florida, the menhaden has considerable tolerance. for high temperatur es. In fact, Bigelow and Schroeder (1953) report that menhaden do not appear in the Gulf of Maine until the water reaches 500F or more. Temperature tolerance data for menhaden are depicted in Figure G.4.2-6. Meldrim and Gif t (1971) reported that the preferred temperature of adult menhaden was 700F with some indication of an avoidance response at 84.20F. .Ba ttelle Columbus Laboratories (1971-72) reported that the 24 hour TIM temperature was 86 F for adults. At 'New England Gas and Electric Compny's Canal Station, menhaden young of the year
. appeared stressed at 870F and were killed when the temperature reached 940F (Fairbanks e t al . , 1971 ) . At the New Jersey Oyster Creek Station, menhaden survived temperatures of 920F but were killed at 990 F (Smith,1974).
( Lewis and Hettler (1968) determined that test temperatures above 33 C0 (91 F)0 caused mortality in young menhaden. How soon they died depended in part on acclimation time, temperature, salinity, D.O., and gill condition. Hoss et al., (1974) reported that larvae acclimated at 10 and 15 C (50 and 59 F) for 3-7 days had a respective upper lethal temperature of 28.9 and 29 7 C (84.0 and 85.5 F).
-The NEP 1 and 2 thermal discharge may interact with this species' nearshore migratory activities anytime during late spring or early f all. During this period, adult and juvenile menhaden could . experience a surf ace water temperature between 53 and 75 F.
Based on the results obtained by the various inv.estigators cited, such a temperature range is well within the temperature tolerance capabilities of this species. As a result of ichthyoplankton studies conducted by Applicant in Block Island Sound, . menhaden larvae and eggs were found at the site from as early as May to as late as October. Observations made .by Hoss et al., (1973) generally indicate that the larval G.4-23
NEP 1&2 ( otage of this species would be able to tolerate an induced surface temperature maximum in excess of the expected 6 F. Since menhaden eggs are buoyant (Bigelow and Schroeder, 1953) there is a possibility that they may be entrained in Applicant's thermal plume. It would be reaso nab le to assume however, that minimal thermal impact would be incurred since spawning and subsequent development of eggs occurs in more southerly wa ters along the eastern seaboard; areas diere water temperatures equal or exceed those predicted in Block Island Sound (NOAA, 1973). In-Plant Effects. The eggs and larvae of the Atlantic menhaden will be subject to entrainment through the NEP 1 and 2 cooling water system, but to dif fering deg rees. Atlantic menhaden eggs were collected from the location of the proposed intake at _ Station BIS-A ~on only one sampling day during the -entire.1974 and 1975 study period . Thus, { due to their limited occurrence, the potential for significant impact to the menhaden population as a result of egg entrainment is minimal. Menhaden larvae, however, were collected from the proposed intake location during late May through late July 1975, and primarily from mid-June through mid-August 1974.- Average larval densities for these time periods are depicted in Figures G.4.2-4 and G.4.2-5. Therefore, due to .their longer tenporal occurrence, the evaluation of entrainment ef fects will ' focus on menhaden larvae. If the plant had been operating at 100% capacity, the estimated number of menhaden eggs and larvae annually entrained through the NEP 1 and 2 cooling water system would have 6 - 7 7 been 0 eggs in 1974 and 8.592 x 10 oggs in 1975,'and 2.027 x 10 and 3. 789 x 10 larvae in 1974 and 1975, respectively. Average annual menhaden egg and larval entrainment satimates for. the two . study years are 4.29.6 x 6 10 eggs and 2.908 x 710 larvae. Making the very conservative assumption that all of the pecjected entrained eggs would have i curviv'e d to the larval stage, then an estimated 3.338 x 107 larvae would annually be ef fected by entrainment at .NEP 1 and 2. G.4-24
l NEP 1&2 ) l The significance of larval entrainmen t losses of the magnitude cited above to the Atlantic menhaden population can be assessed by comparing the above larval entrainment estimates to those predicted for the Pilgrim (Cape Cod Bay) and Millstone (Long Island
~ Sound) nuclear powe r f acilities. The significance of predicted menhaden larval entrainment losses at each of these nearby power facilities was assessed by population simulation modeling (Stone and Webster, 1975; Ho rst , 1976). Since the menhaden population potentially affected by NEP 1 and 2 larval entrainment is identical to the menhaden population modeled for Pilgrim and Millstone entrainment, and if the predicted larval entrainment losses are of similar magnitude for each of the power facilities, then determinations as to the significance of larval entrainment losses made at Pilgrim or Millstone should also be valid for NEP 1 and 2.
'lhe number of menhaden larvae annually entrain'ed through the Pilgrim-Station Units 1 l
f and 2 cooling water , system was estimated to be 1.53 x 108 larvae (Stone and Webster, 1975). Assuming 100 percent larval mortality, this magnitude of larval entrainment at the Pilgrim facility was predicted to cause a reduction in the menhaden population by only 0.0027'S percent over a 50 year period. Since the ef fect of larval entrainment ] at Pilgrim was negligible, Stone and Webster (1975) concluded that the menhaden population should nat be adversely affected.
'Ihe maxista number of menhaden larvae annually entrained through Millstone Station Units 1, 2, and 3 (based on field data) was predicted to be 4 x 10 7larvae (Horst, ~ 1976).
Since this entrairunent prediction resulted in a very small larval mortality coef ficien't,
~
Horst based his p'opulation simula' tion model on highly conservative assumptions. The larval mortality'coef ficient used in his model was 58 times larger than .the -actual entrainment mortality and represented a worst case situation. Utilizing two different simulation strategies (density independent and d'ensity dependent), he predicted that " ^ the menhaden ' population would be reduced in size by only 0.08-1.1 percent af ter 50 years G.4-25
., , . - - - - - - - -e -
-,,c-,, - - < , ,- , , - - , , - - - - - - - - - - - - - - , - - - - - . - - - . - , , - --,,----,,-,-,.n. , - ._- , , , , , . - , , , ,
NEP 1&2 of power plant related mortality. Thus, it was concluded thai, evun when intention' ally overestimating the mortality associated with the power station, no detectable change in the dynamics of the Atlantic menhaden population would result f rom the operation of the Millstone nuclear power facility. Given that the estimated number of menhaden larvae entrained at Pilgrim Units 1 and 2 and Millstone Units, 1, 2 and 3 is over 4.5 and 1 2 times greater, respectively, than the predicted number of larvae entrained by NEP 1 and 2, and given that the Pilgrim Station and Millstone Station entrainment losses had negligible ef fects on the menhaden population, it is concluded that the Atlantic menhaden population will not suffer appreciable harm as a result of larval entrainment at NEP 1 and 2. Total Impacts. Based on historical occurrences at other power plants in southern New England as well as the comparative study conducted by CZC (1979), Applicant believes that the menhaden may be frequently entrapped. However, a significant dif ference between NEP 1 and 2 and all existing New England power plants is that NEP 1 and 2 will have an of fshore, velocity cap intake. This feature should reduce entrapment potential to something less than that observed at other exiting plants. Furthermore, the average critical swim speed of menhaden is generally greater than the intake velocity. Thus, the menhaden swimming capability would allow the fish to swim away from the intake and avoid entrapment. As model studies on the effects of existing plants (notably Millstone and Pilgrim) indicate entrapment effects. have resulted in no appreciable harm to the menhaden population, Applicant believes that this conclusion must also hold for NEP 1 and 2. The menhaden 'is an extremely temperature tolerant species which is known to be capable of living in waters on the order ot' 15-200F warmer than the maximum temperature expected / in the thermal plumes of NEP 1 and 2. Additionally, gas-bubble disease, which is a G. 4-2 6 .
. I
- t NEP 1&2 .
, , temperature related phenomenon, should not contribute to any plant related mortality because of the multiport dif fuser; a detailed discussion of this phenomenon is presented in ER Sec tion 5.1. 4. 4. - As a ' result of the above, it is expected that the menhaden population will suffer little if any, mortality as a result of temperature or temperature related phenomena.
The impact of entrainment of eggs is not judged to be a source of concern since eggs have been taken in the vicinity of the proposed inlet only once in two years. The number of larvae which may be lost within the cooling water system is an order of magnitude less than Pilgrim Station and roughly the same as for Millstone. Models predicting the effects of entrainment at these two plants indicated that the impacts would be insignificant. Considering the high temperature tolerance of the menhaden and the acceptable results I of population inodels at two other southern New England power plants which predict impacts greater than are expected at NEP 1 and 2, Applicant believes that the total ef fect of - the operation of the proposed plants cooling water system will result in no appreciab?e harm to the effected population. 4.2.2 Bay Anchovy (Anchoa mitchilli) 4.2.2.1 Life History.
~
The bay anchovy is a small fish, seldom exceeding 9 cm (3.5 inches) in length, with a range extending from haine to Texas. Its occurrence north of Cape Cod is relatively-rare (Bigelow and Schroeder, 1953). 'It appears to be"found in greatest abundance near river mouths and off sandy beaches, although this may be due to its apparent preference for estuarine areas of spawning. Relatively little has been written about this species, which is o,f no direct commercial value, but which, on the basis of sheer abundance, must play a significant role in the marine food chain. G. 4-2 7 9
NEP l&2 ( he Narragansett Bay ichthyoplankton survey conducted by K1rine Research, Inc., during 1973 (Marine Research, Inc., 1974) indicated tha t the bay anchovy is primari y an estuarine spawner, since the great majority of the eggs were observed in collections made near the head of the Bay. Observations in the area of Ninigret Pond and Block Island Sound during 1975 would tend to agree with this, since egg concentrations at certain stations within the Pond were generally higher than those in the Sound by at least two orders of magnitude. On the other hand, anchovy egg concentrations in Ninig, ret Pond during 1975 were low compared with those observed in the upper regions of Narragansett Bay during 1973, indicating that Ninigret. Pond is probably not of great significance as a spawning area for this species. Kuntz (1913) reported that this species spawns in the waters of f Beaufort, North Carolina from June to August. In Narragansett Bay during 1973 (MRI, 1974) anchovy eggs we re ( collected as early as the first week in June and by late August the eggs had disappeared from the collections. Rese two studies indicate that the spawning season of this species may be roughly the same over a wide genraphic range. Peak egg abundance in Narragansett Bay occurred about the third week in hue, while larval abundance reached a maximum during the second week in August. (It should be noted that, during 1973, the larvae of bay anchovies were more abundant than any other single species in Narragansett Bay, comprising nearly 50% of the total population (Marine Research, Inc., 1974)). During 1974 and 1975, spawning was initiated in Ninigret Pond by late May or by the first week in June, terminating by early September (1974) or by early August (1975). Highest concentrations were found f rom mid-June to mid-July, particularly in the northerly and relatively estuarine area known as Fort Neck Pond. We facts that larval ( concentratione appeared to be much higher in the Sound than in the Pond and that, on one occasion at least, anchovy larvae were found in relatively high concentrations at - G. 4-2 8
~ . - - . . _.
NEP 1&2 . all stations between Qiariestown Beach and Block Island itself, might indicate the major source of larvae to be other than Ninigret Pond. It is perhaps possible that these larvae originated from Narragansett Bay. The temporal abundance of the anchovy ichthyoplankton is presented for Station BIS-A (Figure G.2.2-1) in Figure G.4.2-7, and the spatial distribution within the study area is presented in Figures G.4.2-8 through G.4.2-11. 4.2.2.2 Impacts of Construction. Adult anchovy have sufficient mobility to avoid construction activity, however, increases of suspended sediments and turbidity u. the immediate area of construction may adversely affect eggs and larvae transported through the construction site. Because of the wide range of this species' spawning area, the rapid development of larvae, and the relatively
, . low numbers, these ef fects are expected to be minimal. Under these circumstances, no l
appreciable harm to the bay anchovy population is anticipa ted as a result of construction. 4.2.2.3 Impacts of Plant Operation Entrapment. Bay anchovies are a potential candidate for entrapment since (1) they are a coastal species, (2) their average critical swim speed capability is less than the intake velocity, (3) they are not restricted to a specific stratum in the water column, (4) their planktivorous feeding habit, (5) they are nocturnally active, (6) larger anchovies tend to move to deeper water, and (7) entrapment of h compressa occurs at velocity cap intakes in California. According to Gordon (1974), the bay anchovy in Rhode Island is fo.und in coves, bays and river mouths from May through October. The greatest amount of impingement will probably occur from August when young-of-the-year begin to reach impingible size through October when the exodus from inshore waters is largely completed. The critical swim speed for bay anchovy has been reported by Wyllie
~
G. 4-29 l
- . _ _ _ . -. ~ _ _ _ _ . -- -- -- . __
NEP 1&2 4 ( et al., (1976). Utilizing their data, Applicant calculated the, average critical swim 4 speeds . for anchovy ranging in length from 3 2-3.7 inches and found these swim speeds to be 0. 7 and 1.0 f ps a t test wa ter temperatures of 50 and 59 F, respectively. Section 5.1.4.2 of the Environmental Report discusses the experience and experimental results of Southern California Edison with the velocity cap intake and the anchovy Eng raulis ' mord ax . Although it is likely that some bay anchovies will be entrapped , the numbers are expected to be low because of habitat preferences of the adult -and because of the velocity cap design. 'Ihe location of an of fshore intake should reduce entrapment of the species well below that expected of an estuarine, shoreline intake. Consequently, no appreciable harm to the anchovy population is anticipated as a result i of entrapment. Within the Discharge Plume. The anchovy is a ubiquitous species. found in coas'tal waters ( from Maine to Texas. It is found in decreasing numbers however, north of Cape Cod. Similar to the menhaden, the bay anchovy'is primarily a warm water fish which migrates int'o New England waters during the warmer months (Bigelow'and Schroeder, 1953). The fact that it is abundant in subtropical estuaries where water temperatures may exceed the maximum surface temperature predicted in NEP 1&2's discharge plume (NOAA, 1973) indicates that bay anchovy eggs must be capable of surviving high ambient water temperatures. Houde (1974), conducted experiments on the " critical period" of the bay anchovy in order to determine the post hatching time interval during which larvae must either establish themselves as active feeders or else risk starvation. In' experiments conducted in water- - i temperatures of 24 and 320C (75.2 and 89 60F), survival. ot larval anchovy was achieved
~
when fed 40 to 16 hours, respectively, af ter developmenti of eye pigne t. ca t io n . ( Interestingly enough, the temperatures which were used by Houde were equal to or exceeded G. 4-30
NEP 1&2 the maximum surface temperature anticipated at NEP 1 and 2 by as'auch as 140F (Figure G.4.2-12). Since survival was found even at the highest experimental temperature of 89.60F, no impact is expected for those early life history stages of the bay hnchovy found in the thermal plume of NEP 1 and 2. In preference and avoidance experiments conducted by thldrim and Gif t (1971), adult JL. mitchilli showed a general water temperature preference anywhere from 5 F below to 10 F above the induced surf ace temperature proj ec ted at the site. Of particular relevance is that the highest preference temperature found for bay anchovy (i.e., 860F) exceeds the warmest temperatures observed by Applicant in Block Island Sound. In this instance, the preferred temperature exceeded the expected surf ace maximum water temperature by 10 F. More impo rtantly, however, is tha t in the two cases, where avoidance tests were conducted, anchovy responded to temperatures well in excess of those predicted by the Applicant. Such information indicates that the adult should ( be able to satisfactorily tolerate surface water temperatures incurred f rom plant ope ration. In-Plant Effects. The bay anchovy is one of the four species which were modeled by Stone and Webster (1976). They. analyzed this species with the model which is presented in Section 4.1. 2. 3. In this application, the slightly conservative assumption was made chat the anchovy does not spawn more than once. The survival f rom egg to larvae was estimated to be 0.072 (based on five years worth of egg to larvae ratios from Chesapeake Bay). According to Stevenson (1958) the mean egg production of the bay anchovy is 3 43 x 104eggs; however, only 7% or 2.4 x 103 of these are actually spawned. The latter number was, therefore, utilized by S&W as an estimate of fecundity. In their model, S&W calculated an entrainment rate of 9.919 x 106 eggs and 6.064 x 10 8 larvae based on the 1974 field data. The small dif ference between S&W's estimate and Applicant's estimate (Table G.4.1-2) results fram technique differences in numerical G.4-31
... _. - _ -- . - - - - - _ . - .-_ - ~ _. .- -. . . -
i
, NEP 1&2 .
( ' integ ration: S&W utilized Simpson's rule while Applicant utilized the trapezoid rule. Using the conservative assum'ption tha t all Anchoa s_p. eggs and larva'e were An'choa
'mitchilli and asstating no density dependent compensation mechanism, the above entrainment i ! losses were predicted to result in the loss of approximately 7 x 106 adults. Using I
the same model as S&W and the entrainment rates presented in Table G.4 1-2, Applicant predicts that if NEP 1 and 2 had operated at full load during 1974 and 1975, the losses to the adult population would have been 6.08 x 10 6 and 6.03 x 106 individuals in 1974 i { and 1975, respectively. The assumption of full load is, of course, conservative when 1 . the life of, the plant is considered. A more reasonable load factor would be on the order of 80%; this would produce an annual entrainment loss of approximately 4.8 x 10 6 h l adults. Because no good quantitative studies have been conducted on this commercially
- unimpo rtant species, it is not possible to place the above numbers in perspective.
t However, when one considers tile relative abundance of anchovy ichthyoplankton in Block (. .. Island Sound and areas such as Narragansett Bay, it must be concluded that the former area is not particularly. impo rtant to this species as a spawning area. If the area has comparat' i vely low ichthyoplankton numbers, it follows that the adults lost al'so o constitute a small portion of the population. Applicant, therefore, concludes that I there will be no appreciable harm associated with the entrainment of this species. I 1 Total Impacts. 'The eggs of anchovy are present in low numbers'in Block Island Sound j (as might be expected for a species which has a short incubation period and spawns some !- distance away) and that the larvae and adults are certainly tolerant to any temperatures j which may be encounter'ed in the surface plume. It is also believed that while the I sutrapment potential for this species is judged to be medium to high, the of fshort location of the NEP 1 & 2 intake, as well as the fact that the adults have a preference
; for bays and estuaries, should significantly produce entrapment of this species well i
below that of a shore line intake. 1 1 4 0 G.4-32
NEP 1&2 - Because the anchovy is a forage species of little commercial importance, and no good quantitative studies have been conducted on this species, the conservatively predicted entrainment loss of 7 x 106 adults cannot be directly addressed. However, because the ichthyoplankton density'of this species in Block Island Sound is low compared to nursery areas such as Narragansett Bay, the loss due to entrainment is expected to result in no appreciable harm to the anchovy population as a result of plant operation. 4.2.3 Silver Hake or Whiting (Merluccius bilinearis) 4.2.3.1 Life Histo ry. The silver hake, or whiting, is a strong, swif t swimmer and does not confine itself to a specific stratum in the water column. They are found at depths ranging from the tide line to 400 fathoms (Bigelow and Schroeder,1953). Silver hake often swim together in large numbers but they do not school in definite bodies.
. Silver haka range from Newfoundland to South Carolina. Maximum abundance occurs within the area from Cape Sable to New York (Bigelow and Schroeder, 1953). It winters in relatively deep water, moving inshore in late spring and remaining throughout the summer.
It prefers warmer water than any of the other members of the cod f amily (Olsen and Stevenson, 1975), although seldom occurring in wa ter warmer than 180C (64-650F) . The silver hake is a well armed voracious predator. Their diet includes : alewife, butterfish, cunner, herring, mackerel, menhaden, scup, silversides, smelt, squid and even young silver hake. Silver- hake are of ten seen driving schools of herring ashore (Bigelow and Schroeder,1953). Bigelow and Schroeder (1953) report that the Gulf of Maine is the principal nursery area for silver hake. 'It is probable that' the eggs and larvae of this species which are found in Block Island Sound represent a relatively small f raction of the population G. 4-33
NEP 1&2 as a whole; they were certainly not an important part of the ichthyoplankton sampled during the current study. The largest egg concentrations were collected in mid-June; however, eggs were present in the plankton from late May through August. The eggs are buoyant and hatch within a period of several days. Bigelow and Schroeder (1953) report that the fry move Lat) deep water by autumn; however, during recent years, large numbers have been observed in upper Mount Hope Bay during late fall. By the following spring, the young silver hake range from 5 to 16 cm (2-6.5 inches) in length. According to Bigelow and Schroeder (1953), silver hake remain of fshore until three years of age, when they enter the commercial catch. At this time, they may average 27.5-35 cm (11-14 inches) La length. The temporal and spatial abundance of silver hake ichthyoplankton are depicted in Figures G.4.2-13 through G.4.2-17. The silver hake is an important component of the commercial fishery. In Rhode Island,
~
they constifuted 10% of the total ' landings by -weight. Principal fishing areas include ( the coast of New Jersey, the general area between Montauk Point (Long Island) and Martha's Vineyard Island (including Block Island Sound), and the inshore waters east and north of Cape Cod (Saila and Pratt, 1973)'. In Block Island Sound during 1975, silver hake were found at the otter trawl sampling stations off Charlestown Beach during the months of May, June and July. It was noted that this species occurred in appreciably higher concentrations at the 80-foot depth contour than in the shallower water, 30-40 feet deep (Table G.2 3-3). The catch records of two commercial draggers fishing in slightly deeper water in Block Island Sound during 1975 indicate the presence of silver hake during every month of the year except August. 4.2.3.2 Impacts of Construction. Although silver hake can be found in the area from late spring through the summer, the I adults remain of fshore in deep water. Increases of suspended sediments and turbidity G.4-34
NEP 1&2 in the immediate area of construction could adversely af fect some eggs and larvae floating through the construction site. However, because the density of these life stages are comparatively low in the construction area, these ef fects are expected to be insignificant. he adults are mobile and able to avoid any areas of distrubance. Ilnder these circumstances, no adverse effects on silver hake populations are anticipated as a result of construction. 4.2.3.3 Impacts of Plant Operation Entrapment. Silver hake will be potentially vulnerable to entrapment since they are m oceanic and pelagic. Silver hake have not been found in large numbers in Block Island Sound as far inshore as the proposed intake location. Monthly otter trawl sampling from April 1974 through March 1975 near Station A, the intake location, f ailed to catch a single silver hake. Additionally, gill nets set for six to eight hours at Station (, BIS-A (Figure, G.2.2-1) on ten separate occasions from September 1974 through March 1975 yielded only six silverhake. From May 1975 through March 1976, a commercial dragger made twice monthly sets near the proposed intake and at a point of fshore (near Station BIS-C). he total catch of silver hake of fahore was 330 compared to only 12 near the proposed intake . his data strongly indicates that silver hake do not occur in numbers near the in take , a nd , therefore, will rarely be subjected to. entrapment. For those few silver hake that do occur near the intake, entrapment is not believed likely. According to Bigelow' and Schroeder (1953), silver hake are strong, swif t swimmers. In addition it is anticipated that this species will be adequately protected by the velocity cap intake particularly since there is no entrapment record of its count.erpart . species, the, Pacific hake (Herluccius productus) at operating velocity cap intakes in California. We impact of entrapment on the silver hake population is, ( therefore, expected to be insignificant. G. 4-3 5
NEP 1&2 Within the Discharge Plume. The silver hake is a cold water fish as are all members of the family Gadiae. Bigelow and Schroeder (1953) report that the adults are not found in abundance above 640F. Because of their swimming ability adults are not expected to be affected by the plume. Most eggs are apparently spawned at water temperatures between 45-55 F; however, the eggs are buoyant and apparently incubate most successfully at temperatures of 55-600F (Bigelow and Schroeder, 1953). During 1974 and 1975, applicant has observed eggs and larvae at temperatures of 49.1-76.60F and 56 3-73 4 F, respectively, at some locations in Block Island Sound. The temperatures of peak abundance for egg and larvae were . roughly 62. 6-71. 60F and 5 9-6 8. 9 0 F, respectively. If we make. the very conservative assumption that each of the two early life stages will not survive if exposed to temperatures above those observed, then both the eggs and larvae will be viable throughout the major period of presence and only a very small number will be' killed ( at the end of the s3 awning season. r Additionally- , it must be noted that most of the Block Island Sound eggs and larvae were
/ t Furthermore, the densities r)ound anywhere 'were low, found at the offshore stations.
indicating that J1ock Island Sound. is not an important spawning area. The Gulf of Maine is probably this species' most prolific nursery area (Bigelow and Schroeder, 1953). 1 It is, therefore, concluded that the thermal discharge will have little or no ef fe.ct on the silver haie population. l In-Plant Ef fects. Silver hake eg'gs occurred at the location of the proposed intakes for approximately 84 days and 56 days during 1974 and 1975, respectively. Silver hake
. larvae occurred.fo r 49 and 5 6 days , respectively, during the same. period.
(' Based on the calculated densities of silver hake eggs and larvae and assuming a 100% Pl ant load during their period of occurrence, 3.054 x 107 eggs and 8.614 x 105 larvae G. 4-3 6' ,
NEP 1&2 i would have been entrained in 1974 and 1.108 x 108 eggs and 4.281 x 106 larvae would have been entrained in 1975. Entrainnent may be compared to either the equivalent number of females necessaqr to produce the number of eggs and larvae entrained or to the number of sexually mature silver hake that would have developed f rom the entrained eggs and larvae. The model utilized to evaluate entrainment losses with respect to the adult population is the same as that presented in Section 4.1.2.2. . Based on two years worth of larvae / egg ratios collected by Applicant at Cha rlestown , the survivorship from egg to larva (Se ) is 0.033. In the model, F. represents the fecundity of a breeding pair during their life. Since the available data does not allow - the prediction of a lifetime fecundity, this analysis conservatively assumes that an individual female spawns only once; Sausken and Serebryakov (1968) present an average fecundity value of 343,000 for 25-30 cm females. As adults average 14 inches (35.6 cm) (Bigelow and Schroeder, 1953) this fecundity-is probably conservatively 1ow. 2 From { this information, it is calculated that the survivorship from egg to adult is: 2 S- - 5.8 x 10-6 343,000 and survivorship from larvae to adult is S t 5.8 x 10 1. 8 x 10-4 0.033 The loss due to entrainment, therefore represents (3.054 x 107 )(5.8 x 10-6) + (8.614 x 105 )(1.8 x 10-4) = 332 adults during 1974 and
. (1.108 x 108 )(5.8 x 10-6) + (4.281 x 106 )(1.8 x 10-4) .1413 adults s during 1975.
If the projected loss is conpared only to spawning females, the 1974 and 1975 entrainment projections equate to 166 and 707 individuals, respectively. G. 4-3 7
NEP 1&2 If the average weigt5t of a mature silver hake is assumed to be one pound, then the equivalent loss of gravid females from entrainment in 1974 and 1975 is equal to 0.003% and 0.01% of the 1975 Rhode Island commercial silver hake landings (5,347,000 pounds). Similarly, the number of silver hake that would have developed from the entrained eggs and larvae is equal to 0.006% and 0.02% of the Rhode Island silver hake landings in 1975.
'Ihese numbers are considered to be very conservative, but even if valties by two orders of magnitude higher were assumed, no appreciable harm to the silver hake population is predicted as a result of entrainment.
If is, therefore, believed that the impact of entrainment on the population of silver hake will be insignificant. Total Impacts. %Alile the silver hake is an ,important commercial species in the deeper ( waters of Block Island Sound, neither the adult nor ichthyoplankton is common in the vicinity of the proposed intake and discharge. This lack of abundance by itself is enough to conclude that the operation of NEP 1 and 2 will not have a significant ef feet on the Block Island Sound population. Additionally, the eggs and larvae have been observed in Block Island Sound at temperatures approaching those expected in the thermal plume, and the adults are quite capable of avoiding both the plume and the intake currents. Furthermore, there is no record of its counterpart species, the Pacific hake, being entrapped' at operating velocity cap intakes in California. It is, therefore, concluded that there will be no appr.eciable harm to the silver ~ hake population as a result of, plant operation. G. 4-3 8
NEP 162 . 4.2.4 Striped Bass ,(Morone saxatilis) 4.2.4.1 Life History. t On the Atlantic coast, the range of the striped bass extends from the St. Lawrence River to Louisiana (Phrriman, 1941). Its center of abundance is the mid-Atlantic Bight region
-(Cape Cod to Cape Hatteras) where 80 percent of the commercial catch is taken and idiere most of the recreational fishing for this species takes place (Saila and Pratt, 1973).
The striped bass is a migratory species that may travel considerable distances along the coast during spring and fall. The majority of bass caught along the shores of southern New England during late spring , summer and early f all originate f rom the Chesapeake Bay area, where they hatched and where the maj ority return each f all. According to Chapoton and Sykes (1961), large bass tend to winter along the coast of North Carolina. According to Herriman (1941), both the spring and fall migrations are { triggered by water . temperatures of approximately 70C (450F) . These populations are
- supplemented to a certain extent by fish originating in the Chesapeake (Saila and Pratt,
, 1973). The striped bass is a carnivore, although not particularly discriminate in its feeding
~
habits. It is evident from Raney's (1952) review of the subject tha t' smaller fish constitute the bulk of its diet, with such species as silversides, menhaden, mummichogs and anchovies being particularly prominent. However, various inverteb rates such as prawns, crabs, snails and clams are also included This is an anadromous species that spawns in the major tributaries draining into the mid-Atlantic. Major spawning areas include the rivers entering Chesapeake Bay, Pamlico and Albanarle Soteds in North Carolina, and, to a lesser extent, the Delaware and Hudson t Rivers and smaller rivers to the north. Bass reportedly spend their first two years in the estuary in which they hatched. The males tend to mature somewhat more rapidly G.4-39
NEP 162 than the females, reaching sexual maturity by the end of their second or third year, whereas the majority of females do not become mature until their fif th year. Bass have been known to attain a weight of 125 pounds, although such fish are exceptional (Bigelow
- and Schroeder, 1953).
Charlestown Beach is reportedly a favored area for recreational striper fishing, which is done both from the shore and from boats working off the beach. The results of gill netting in Ninigret Pond during 1975 indicated that bass were present as late as November. Although bass have been known to winter over in New England ' estuaries, there is no evidence that they have done so in Ninigret Fond during the past few years. 4.2.4.2 Impacts of Construction. f The adults are found in the area from spring until f all, but they have sufficient mobility to avoid the construction activity. However, it *is possible that because of their feeding habits and food preferences, they may be attracted to the site during . construction to take advantage of aquatic organisms dislodged during construction. 1 Because no eggs or larvae are present, they will not be affected. Under these circumstances, no appreciable harm to the striped bass population is anticiapted as a result of construction. 4.2.4.3 Impacts of Plant Operation Entrapmen t. The pelagic striped bass is a possible candidate for entrapment since this migratory species adheres to the coastline during its movements. The striped bass is, f however, not expected to be entrapped more than occasionally for the following reasons. i According to Bigelow and Schroeder (1953), striped bass do not migrate until they are i two years old. Juvenile striped bass, which would be most vulnerable to entrapment (CZC,1979), do not occur. in Block Island Sound. Fish older than two years potentially i G. 4-40 i
-- , . . - - - . , , , ,.. .- . . - . - . . - . . . , , . . . , , , . - . - . - . , - . _ , , ~ - -,, ..
NEP 1&2 could be entrapped. The average size of two-year old striped bass .in the vicinity of Block Island Sound is 11 to 11.5 inches (Bigelow and Schroeder, 1953). Bibko et al. (1974) have reported that striped bass 3.5 to 8.6 inches in length have averagAt swim speeds ranging f rom 1.6 to 2.8 f ps. Since the striped bass that would be found in the region of the intakes should be approximately 11 inches or greater in length, their swim speeds would probably be greater than those for the smaller individuals reported above by Bibko et al. (1974). Thus, striped bass in Block Island Sound are. believed to be strong enough to avoid or escape from the intakes, and Applicant is unaware 'of any significant entrapment problem with this species at other power plants in New England . Furthermore the west coast counterpart, Cynosicion nobilis, was entrapped by velocity cap intake in low numbers in 23% of the samples evaluted by CZC (19 7 9) . They de termined that only 156 individuals were impinged on 121 sample da tes. The impact of entrapment on the striped bass population is, therefore, expected to result A,, in no appreciable harm. Within the Discharge Plume. The importance of -the striped bass (Morone saxatilis) as a sport fish is undoubtedly the reason for the large amount of available information on its thermal tolerance (Figure G.4.2-18) . Tagatz (1961) has shown that adults.can tolerate abrupt changes between saltwater and freshwater at temperature dif ferences between 45 and 80 F. Similarly,_ juveniles tolerate. temperatures between 55 and 69 F. Meldrim and Gif t (1971) in their temperature shock studies quickly increased test tank temperatures from 79 to 940F, held this temperature for fif teen minutes, and then returned the fish to ambient conditions. This temperature regime was survived by all test stbjects but there were some mortalities in two similar studies in which bass were acclimated at 660F before the +150F temperature pulse. Another aspect of this investigation gathered data on the ability of striped bass to avoid areas of elevated water temperature. Maximum upper avoidance temperatures of 93 and 94 F were found for G.4-41
NEP 1&2 (
^
bass acclimated to 810F, while those acclimated to 41 F in winter avoided 550F waters. Observations made by Dorfman and Westman (1970) indicate juvenile bass may survive and even feed at 95 F for short periods whereas Talbot (1964) cites Merriman (1941) who indicates that striped bass in New England can tolerate maximum temperatures of 77 to 800F. Gift and Westman (1971) in their study increased water temperatures f rom an initial acclimation temperature of 680F by 0.61010F/hr until 8012 F was reached.
'Ihereaf ter, the temperature was raised 2. 510. 50F/hr un til an avoidance breakdown response was realized (avoidance breakdown is defined in Mihursky and. Kennedy, 1967, as CIM) . The results of their study indicate that striped bass ranging in length from
~
48.3-55.9 cm had an upper avoidance breakdown temperature of 86 F. As discussed in the species' life history characteristics, the majority of bass caught along the shores of southern New England during late spring, summer, and early f all ( ' originate from the Chesapeake Bay area, where maj or stock rec ruitmen t to existing populations takes place. Inasmuch as spawning and development of juveniles up to two years of age takes place in these more southerly waters, the plant discharge will in no way affect these stages in the species' life history. he possiblity of interaction. with the NEP 1 and 2 thermal discharge could arise during the species' migratory activities anytime during late spring or early f all. During this six to seven month interim, striped bass could encounter a plant induced surface water temperature, anywhere from a low of $30F to a high of 750F. his is certainly well within their temperature tolerance capabilities. In-Plant Effects. Because no striped bass ichthyoplankton are present, there will.be no in-p_lant effects. Total Impacts. The only striped bass which will be potentially susceptible to ef fects resulting from operation of the NEP i and 2 cooling water system will be age two or older. 'Ihese individuals may be subject to entrapment. Because they are fast swimmers G. 4-4 2
- ~ - - _ . _ - - .- - ..
NEP 1&2 + which have apparently not been entrapped in significant numbers at other power plants-in New England (nor are th'eir ecological counterparts entrapped in great numbers in California), it is believed that they will not be entrapped la large numbers a t the proposed plant. It is concluded that the striped bass population will not suffer appreciable harm as a result of the operation of NEP 1 and 2's cooling water system. t ( l\ T v l
.G.4-43
. - _ - _ _ _ _ _ .- , . . . , _ _ _ _ - . , . _ - _ . . _ _ - ~ . .
NEP 1&2 ( t 4.2.5 Bluefish' (Pomatomus saltatrix) 4.2.5.1 Life History. Tne bluefish is a widely distributed species that supports an active recreational fishery from Maine to Florida. Depending upon the time of year, it may occur along the edge of the outer continental shelf, at depths of 100 fathoms or more, or may be 'found well within coastal estuaries. The wintering grounds of bluefish that occur in the inshore waters of southern New England are not known with certainty, since adults have been captured during winter bo*.h in the deep waters at the end of the shelf as well as along the coast of Florida (Saila and Pratt, 1973). By March and April, bluefish appear of f the Carolinas, of f Delaware in April, and off New Jersey and New York in April and May. They usually first enter the waters of southern Massachusetts in early June and, in recent years , move f eastward of Cape Cod and into the wa te e s o f Ha in e later in the summer. When water temperatures drop to 12-15 C (54-59 F) in. fall, the bluefish depart the coastal waters of southern New England. According to Lund and Ha' tezos (1970), adult fish move of fshore, while young of the year and Age 1 fish migrate southward along the Coast. Bluefish spawn of fshore in early summer, a major spawning ground apparently lying 30-80 miles off the Virginia-Worth Carolina coact tRorcross et ei., 1974). The larvae are roughly 2 mm in l'ength at hatching. Juvenile fish gradually work their way inshore during late summer and fall, and form schools of " snappers". At this time the fish may range from 10 to 200 cm (4-8 inches) in length. When 'one year of age, bluefish av'erage 20-3d 'cm '(8 k 2 inches): in length (Bigelow and Schr'oeder', 1953)i they probably i become sexually mature when three years of age. Bluefish grow rapidly and feed voraciously upon a variety of forage species. Included G. 4-4 4
NEP 1&2 in their diet are menhaden, mackerel, herring, hake, butterfish, and squid (Olsen and Stevenson, 1975), as well as sand lance and silversides. As indicated above, the bluefish is an Offshore spawner, and neither its eggs or l'arvae have been observed in the ichthyoplankton collections from Block Island Sound or Ninigret Pond. However, large numbers of young of the year enter Ninigret Pond in late summei and remain into November. 4.2.5.2 Impacts of Construction. Both the " snappers" and adults are found in the vicinity during the warmer months; he.ever, they have suf ficient aobility to avoid construction activity. Because no eggs or larvae are present, they trill not be af fected. Under these conditions, it is concluded that construction activities will have little or no ef fect on the bluefish. 4.2.5.3 Impacts of Plant Operation ( Entrapment. Because the bluefish is pelagic and migrates close to shore, it is a possible candidate for entrapment. Swim speed studies, however, indicate that the 1. 5 f ps intake velocity proposed for NEP 1 and 2 is suf ficiently low to adequately protect even the young bluefish which appear in southern Rhode Island during late summer and fall. Wyllie et al., (1976) conducted numerous swim speed tests with young bluefish (NEP 1 and 2 Environmental Report, Table 5.1-1) . For bluefish in the size range of 3.1-7 5 inches, they observed critical swim speeds of 1.6-3.2 f ps with an average value of 2.1 fps. Olla and Studholme (1971) studied the ef fect of temperature on the average daily swimming speed of adult bluefish which were 55-65 cm long. They observea daily averages on the l , order of 1-1.5 fps when acclimated to a temperature of approximately 200C (68 F). As G.4-45
NEP 162 the temperature either increased or decreased f rom the acclimation temperature, the average swimming speed increased to approximately the same value (2.6-3 0 f ps) at temperatures of approximately 120C and 30 C (540F and 860F)'.- It appears that swimming speed increases as a result of stress and that adult bluefish are capable of sustained daily average speeds of a t least ' 3 f ps; burst speeds are certainly higher still. During their ccuparative entrapment study for NEP 162, CZC (1979) indicated that although yearling bluefish are present throughout the winter in the vicinity of the velocity cap intake a t St . Lucie, Flo r id a , no bluefish have been impinged .t that plant. As a result of the swim speed capability of both adult and juvenile. bluefish as well' as the lack of entrapment of this species at an operating velocity cap intake in Florida, Applicant believes that bluefish will very rarely be impinged. Within the Discharge Plum According to Bigelow and Schroeder (1953) bluefish are ( . ever found in any numbers where water temperatures fall below 58-600F. As reported in the life history section for the bluefish, it is believed that spawning takes place in early summer apparently of f the Virginia-North Carolina coast. As a consequence, no thermal impact upon the egg and larval life history stages is anticipa ted. Any interaction that occurs between the plant thermal discharge and the bluefish will involve the juvenile and adult life histo ry s tages. Due to the migrational characteristics of this species, however, such interaction is expected only during the late spring and the early fall (Figure G.4.2-19) . Gordon (1974) has personally. observed bluefish in Rhode Island waters from June to late November. During the six to seven month interim, bluefish coul'd encounter a plant induced surf ace temperature, anywhere from a low of 58 F to a high of 75 F. Much has been written concerning the temperature tolerance of the juvenile or " snapper" ( life history stage of the bluefish. Most if not all of tihe published literature G. 4-4 6
NEP 1&2 indicates that the bluefish is a very hardy species from the standpoint of thermal tolerance. In temperature preference studies conducted Ly Meldrim and Gif t (1971), juvenile bluefish ranging in size f rom 78-125 mm we re acclimated between $5' 75 F. - 0 When 53-62 Corresponding preference temperatures were observed between 72 and 83 F. mm fish wre acclimated at 72 0F, an avoidance response was observed at 89 F. In testing responses of some estuarine fishes to an increasing thermal gradient, Gif t and Westman (1971) found that 7.9 cm (average) bluetish pad a mean avoidance temperature of 86.50F and a mean avoidance breakdown response at 92.0 F. Similar results were observed for somewhat larger fish (13 9 cm) where respective mean avoidance and avoidance breakdown temperatures of 88 and 92.5 F were found. 011a and Studholme, (1971) tested the ef fects of temperature on the behavior of marine finfish species, which indicated juvenile bluefish swimming activity was found to
. increase significantly as water temperatures rose above 27 C (81 F) . Swimming speeds a
continued to increase until reaching a maximum at 32-33 C (89 6-91.4 F). Loss of equilibrium occurred between 34.5-35.6 C (94.1-96.1 F). Interestingly, Olla and Studholme (1971) interpret an increase in swim speed when temperatures were raised to a point as a response, at least in part, to a manifestation of avoidance behavior to thermal regimes which departed significantly f rom their preferred temperature. Their swimming behavior results coincide quite closely to the avoidance response temperature noted earlier by Gif t and Westman (1971) and Meldrim and Gif t (1971). In addition preference studies conducted by Wyllie et al. (1976), showed juveniles were acclimated from 64.40F to 770F. Preference tempe ra tur e results ran from a low of 71.60F (acclimation temperature: 68 F) to a high of 79.7 F (acclimation range: 71.6-77 0 F. Daese same authors observed an avoidance response at 87.2-89 6 F when acclimated to 68 F. Finally, in a most recent study in which preference and avoidance. responses were once again tested, juvenile bluefish were found tolerant of water temperatures well in excess of those anticipated as a result of plant operation. Preference studies C. 4-4 7
-NEP 1&2 conducted by Terpin et'a1. (1977), indicates that juvenile bluefish acclimated to water (
temperatures from 50 to 73 4 F show water temperature preferences from a low of 64 90F when ' acclimated at 500F, to 77 9 F when acclimated at 73.4 F. In avoidance studies, juvenile bluefish (108-195 mm) were acclimated to a temperature range of 59-77 F. A low avoidance temperature of 86.7 F was observed f or a corresponding acclimation temperature of 590F while the high was found to be 95.50F 'at an acclimation of 770F. Again, these results indicate that juvenile bluefish can easily tolerate the surface maximum temperature induced by the plant. Olla and Studholme (1971) subjected adult bluef tsh (55-65 cm). to swimming tests at varying temperatures above and below their 19-20 C (66-680F) acclimation temperature. At a temperature of 39 8 C (85 6 F) they observed a significant change in the adult's average swimming speed and schooling ability which they interpreted as indicative of stress or an avoidance response. It is interesting to note that this avoidance response exceeds the highest induced surface temperature expected at . the Applicant's thermal discharge by 10 F. In summary, the pubitahed thermal tolerance studies relative to the juvenile and adult life history stages of the bluefish indicates that this species would be very tolerant of any surf ace temperature chanae that NEP 1 and 2 could induce. En t rainmen t. Because bluefish do not spawn in the nearshore waters of southern New England, this species will not be subjected to entrainment. Total Impacts. Because eggs and larvae of the bluefish are not present in Block Island Sound, entrainment of this species is not an issue. Likewise, because all affected life stages are highly motile, there should be no construction-related ef fects. While both the juveniles and adults will be subject to thermal plume interaction and possible entrapment, Ap pl ic an t has documented that the species is too tolerant of high i i G.4-48 r
- - + , . --- , - - ,
NEP 1&2 temperatures to be affected by the thermal plume and too fast to be frequently entrapped. Consequently, Applicant believes that there will be no appreciable harm to the bluefish populatio'ns f rom the operation of the circulating wa ter system of NEP 1 and 2. 4.2.6 Scup (Stenotomus chrysops) 4.2.6.1 Life His to ry . Scup is a moderately important commercial and recreational species between southern New England and Cape Hatteras. Cape Ann, Massach us e t t s is the northern boundary of the scup's usual range; however, they are found inf requently as far north as Eastport, Maine (Bigelow and Schroeder,1953). In the vicinity-of Rhode Island, it appears that the fish arrive in three distinct cohorts, the first arrivals we igh 1-1/2 to 2-1/2 pounds, the next 3/4 to 1 pound, and the latest arrivals weigh 1/4 to 1/2 pounds. The size definition of these groups is more clearly evident in some years than in others (Neville and Talbot, 1964). During Applicant's studies, scup first ( appeared in April and were an important part of the commercial catch from May through November. Scup move of fshore and southward with the chilling of coastal waters in the fall. The extent of this acvement is a function of the climatic conditions of the particular year. These fish and thase enteri. g the winter fishery along the mid-Atlantic states are believed to be subscantially of the same stock (Neville and Talbot, 1964). Young-of-the-year fish were identified at the site during experimental trawls of late summer and fall of 1975. Relatively few scup eggs and larvae have been observed in the ichthyoplankton collections, suggesting that this ' sector of Block Island Sound is not a particularly f avorable spawning area. The temporal and spatial distribution of the eggs and larvae are presented in Figur es G. 4. 2-2 0 throug h G. 4. 2-2 4. Scup are primarily bottom feeders which prefer smooth to broken ground. They feed on G. 4-4 9
N EP - l& 2 small crustaceans, worms, sand dollars, hydroids, squid and other similar prey (Bigelow ( and Schroeder, 1953). s Prior to 1900, the scup was an impo rtan t component of the trap fishery. Since then, the trap fishery has declired and most scup are now taken by otter trawl. The majority of the total harvest is by sport fishermen utilizing hook and line (Gusey, 1976). 4.2.6.2 ~ Impacts of Construction. Schools of adult scup are sufficiently mobile to avoid suspended sediments and turbidity; however, it is possible tha t they may be attracted to the construction area in Block Island Sound to feed on dislodged marine organisms. In the immediate area of construction, eggs and larvae could be af fected; however, relatively few scup eggs and larvae have been observed in Block Island Sound. This suggests that the area is not a favorable spawning area. Under these circumstances, no appreciable harm to the scup population is anticipated as a result of construction. 4.2.6.3 Impacts of Plant Operation Entrapment. Scup, since they are an inshore fish during the warmer months (Gussey, 1976), will be potentially vulnerable to entrapment. Entrapment of scup is expected to be minimal however, (particularly during daylight hours) because of the following reasons. The location of the proposed intake does not appear to be in an area which might be considered prime habitat for scup. Secondly , they are strong-swimming fish capable of sustained swimming speeds in excess of five body lengths per second and even higher burst speeds. For example, Wyllie et al. (1976) have,shown that this species has a critical swim speed of 1.8-2.3 fps which would allow these' fish to avoid or escape the intakes. In addition, scup tend to hug the bottom during daylight hours thereby reducing the likelihood of diurnal capture by a midwater l intake structure. . Also scup are exceedingly wary fish; they are seldom. seen by SCUBA ( divers despite their great abundance (this is in marked contrast to easy observation G.4-50
NEP 162 of sargo and walleye surf perch -in Califo rnia) . Lastly, scup are not conspicuous in the impingeinent sample of coastal generating stations with convention'al shoreline in' takes s (CZC, 1979). Consequently, the impact of entrapment is not expected to result in appreciable harm to the scup population. Within the Discharge Plume. Bigelow and Schroeder (1953) report that scup are so sensitive to low water temperatures that large numbers have been known to perish in sudden cold spells in shallow wa ter. Neville and Talbot (1964) and Thompson et al., (1971), both describe an avoidance response to water temperatures of .450F or below. The likelihood of thermal impact upon the adult life history stage of this species is anticipated to be minLnal for several reasons. First, the range of this species implies that they exist in waters where temperatures equal or exceed those anticipated as a result of plant operation (NOAA, 1973). Second, adults can move from an area should ( it prove unsuitable. Similar to the adults, any impact upon the early life history stages of this species resulting f rom the thermal plume is expected to be negligible. Incubation of scup eggs is reported to occur at water temperatures which are almost equivalent to the warmest temperatures projected at the site; scup eggs are buoyant with incubation occurring in 40 hours at 72 0F (Bigelow and Schroeder, 1953). Additionally, very low numbers of eggs and larvae were found in the ichthyoplankton. In-Plant Effects. Scup eggs were present at the location to the proposed intake for 91 and 56 days in 1974 and 1975, respectively. .Scup larvae for the same periods occurred for 42 and 44 days, respectively. If NEP 1 & 2 had been operating at full load during the period when scup eggs and larvae ( were present, 2.946 x 107 eggs and 2.169 x 106 larvae would have' bedn entrained in 1974. During 1975, 1.299 x 108 eggs and 7.429 x 106 larvae would have been entrained. G.4-51
._ .m . . . ._. . - _. . . _ ._ _. _ _ _ . _ _. - _ _
l NEP 1&2 The entrainment can be equated to the number of sexually mature scup that would have developed from the entrained eggs and larvae by assuming that, during her life, a, single
- female produces only two offspring which reach sexual maturity. The calculations are the same as described in Section 4 1.2.2.
i The fecundity of the scup was estimated in the Jamesport 316 demonstration to be -30,000 ! eggs. This estimate is based on a relationship between maximum egg size and ' minimum body weight. This estimate is considered conservative. For comparison, P. A. Isaacson of the New York Public Service Commission, in testimony before the New York State Board , of Electric Generation, Siting and Environment, Case 80003, estimated the lifetime fecundity of scup to be 250,000 and the annual fecundity to be 144,000. His estimates were based on the analysis of three fish. The average spawning life of the scup is estimated to be 1.25 years by assuming an 80% annual mortality (Finkelstein, 1971). Therefore, based on the conservative fecundity estimate of 30,000 eggs, the average sexually mature female scup -produces 37,500 eggs during her spawning life. Since the scup egg has a relatively short incubation time of two to three dayr (Bigelow and Schroeder,1953), the egg to larval ratio is considered an estimate of the egg-to-larval survivorship. The average egg-to-larval ratio for 1974 and 1975 for all Block Island Sound Stations is 10 to 1.- The average egg to larval ratio for Station A is 15 5 to 1. The best estimation of the actual egg-to-larval ratio is based on the maximum number of stations. However, since the higher egg-to-larval ratio adds conservatisms to the calculation, it will be used. The larval entrainment in 1974 and 1975 is, therefore, equivalent to 3 36 x 1.0 7 and 1.15 x 108 eggs, r e s p e c t iv e l'; . Based on t;he total spawning life fecundity, the predicted egg 'and larval entrainment. I and the assumption that only two sexually mhture scup will develop f rom the lifetime G.4-52
---m--,
NEP 1&2 s pawn , the entrainment by NEP 1 an1 2 during 1974 and 1975 would have resulted in a loss of 3,360 and .13,100 scup, respectively. If the average scup is assumed to weigh. 1 pound, then the entrainment is equal to 3,360 and 13,100 pounds of scup for 1974 and 1975 respectively. The Rhode. Island commercial scup landing for 1975 was 5,357,000 pounds. However, the average Rhode Island commercial scup landing for the years 1971, 1973 and 1975 was 3,802,000 pounds. Since the lower number adds to the conservatism, it will be used. The number of scup potentially lost due to entrainment in 1974 and 1975 is, therefore, equivalent to 0.08% and 0 3%, respectively, of the average commercial scup landings. These estimates are considered conservative, but even if the value is an order of magnitude greater, the loss of scup is predicted to result in no appreciable harm to the population. -( Total Impacts. The scup is a warm water species which exists seasonally in New England. It naturally exists in waters warmer than will be found within the thermal plume, and there should be., therefore, no, impact frcin this source. Entrapment is likewise expected to present no significant prob!am: (1) because of the relative scarcity of scup inshore; (2) because of their ralative strong swimming capability, (3) because they apparently- have not proven vulnerable to en'trapment at other power plants in New England, (4) because of their preference for the bottom during daylight hours thereby reducing the likelihood of capture by aid water intake, and (5) because scup are exceedingly wary fish. Scup eggs and larvae are present in relatively low densities in Block Island Sound. Because this is not an important nursery area, entrainment will be equivalent in effect
^
to less than one-half percent of the Rhode Island commercial scup landings. G.4-53
NEP 1&2 It is concluded that the scup population will not suf fer appreciable harm as a result . ( of the operation of NEP 1 and 2's cooling water system. - s 4.2.7 Cunner (Tautogolabrus ~ adspersus) 4.2.7.1- Life History. The cunner is. a small, predominately coastal fish which, in New England waters, is found from the tide mark seaward among rocks, pilings and algal fronds (Bigelow and 9eder, 1953). The range of the cunner extends from the Gulf of St. Lawrence to the Chesapeake Bay (Johnsen, 1925; Bigelow and Schroeder, 1953). It is a ubiquitous species of little direct commercial or recreational' value and one generally regarded as a nuisance to fishermen. The cunner is an omnivorous species. As larvae, the food consists chiefly of small crustaceans copepods, amphipods and isopods. According to Shumway and Stickney (1975), the diet of .the adult. cunner in Narragansett Bay consists primarily of the barnacle. k (Belanus balanoides) and two species of bivalve mollusks, the Atlantic sea auss'el ( Mytilus edulis) and the sof t shell clam (Mya arenaria). Other forms represented in the cunner's diet included various species of macroscopic algae, sponges, coelenterates,. polychaete worms, c rustacea, mollusks, b ryozoans, a sc id ia n s , and small fish. In Block Island Sound, Labrid-Limanda eggs (the cunner, tautog and yellowtail flounder eggs tere generally grouped because 'of the difficulty in dif ferentiating them) occurred in the collections primarily during the period 22 May - 24 July 1974, and 20 May - 23 July 1975 (Figure G.4.2-25). Peak abundance of eggs occurred in the Pond at the sampling ,ctation nearest the breachway, suggesting that some if not most, of these had orginated in the Sound and were swept into the Pond by the tide. In Block Island Sound, the eggs were found in highest concentrations at the sampling stations nearest shore and east of Minigret Pond's breachwey (Figures G.4.2-26 and C.4.2-27). [ Imbrid-Limanda larvae were extremely rare in the Ninigret Pond collections, particularly G.4-54 4
NEP 1&2 in comparison with those from Block Island Sound. Larvae were generally abundant between marlestown Beach and Block Island and comprised a high percentage of total larvae during the stamer months. At the age of one year, cunner are approximately 5 cm (2 inches) in length. After two years, they are approximately 10 cm (4 inches) and .af ter three years, 15 cm (6 inches) . At. the age of six years, length may average 25 cm (10 inches) (Bigelow and Schroede,r, 1953). Observations by Serchuk and Cole (1974) in the Weweantic River estuary in Massachusetts suggest a somewhat lowe r rate of growth, i .e . , fish three and six years old average 12.5 cm and 20.4 cm in length,' respectively. The temporal and spatial distribution of cunner eggs and larvae (Labrid-Limanda group) are depicted in Figures G.4.2-25 through G.4.2-29. 4.2 7.2 Impacts of Construction. Cunner are mobile enough to avoid construction _4 activities; however, it is possible that they will be attracted to the site during construction to feed on the displaced bottom organisms. It is, also, possible that increased suspended sediments and turbidity in the immediate area of construction may adversely affect eggs and larvae passing through the construction site. However, because of the short time interval and area involved, and because the cunner is not at great commercial or recreational value, and because of its great. abundance in Block Island Sound, no appreciable harm to this species is anticipated as a result of construction. 4.2.7.3 Impacts of Plant Operation Entrapment. The cunner is one of the species which may be entrapped regularly in relatively low numbers since they are an abundant coastal fish closely associated with rocks, pilings and underwater structures, and small cunners are not strong swimmers.
' Underwater site inspection revealed that cunner do inhabit the area of the proposed in take . The level of entrapment is not readily predictable since no density statistics G.4-55
I i NEP L&2 l l are available for cunner at the intake, site. The impact is, however, expected to be ( l highly localized since cunner are non-migratory, and according to Bigelow and S'cht,oeder - { (1953), they never depart from the bottom or rocks about which they make their home. l Since the bottom in the vicinity of the intake is characterized by non-continuous rocky outcrops, only those cunner inhabiting the immediate area of the intake will be readily vulnerable to entrapment. Those living in the surrounding areas should be less likely 1 to be entrapped, becoming vulnerable only when they move into and repopulate the intake l l area. Other factors which would suggest that entrapment of cunners sho' '.d not be very significant include: (1) there has been a low entrapment of their counterpart species, the opaleye, in southern California, (2) cunners are inactive at night and not available in the winter,- (3) the largest cunners tend to inha. bit deeper waters, (4) cunners are l
- grazers and are well adapted to wave surge conditions (CZC, 1979).
l i The impact on the cunner population 'is, therefore, predicted to be insignificant. ( Within the Discharge Plume. As reported earlier, the cunner is a ubiquitous species found in abundance along the Rhode Island coastline. 1 l Haugaard and Irving (1943) reported that the cunner can tolerate water temperatures i as high as 29-30 C (84.2-86 F) af ter existing at a field temperature of 18-22 C (64.4-71.60F). They also reported that test fish acclimated to winter temperatures of 1-30C died when ' test temperatures exceeded 25-260C '(7 7-78.80F) . DeSylva (1969) corroborates i the summer test observation made by Haugaa. d and Irving by reporting an upper lethal temperature of 84.20F. Based on field data collected 'at the s'ite, Applicant observed that cunner spa'wn during the months of Nky-August at temperatures ranging f eca 15 C (59 F) to 200 C (68 F), whereas . Bigelow and Schroeder (1953) describe a somewhat broader spawning ' range of 55-72'F. I Hatching usually occurs within two days a t temperatures of 70-72 F-(Bigelow and C.4-56 -
NEP 1&2 Schroeder, 1953). From a. temperature tolerance standpoint, the cunner appears to be a hardy species, able to withstand test temperatures as high as the mid to upper-seventies during the winter and the mid-eighties during the warmest summer months. This species' upper temperature tolerance makes it well suited to withstand the six degree surf ace temperature increase anticipated within the boundary of the mixing zone. The temperature information on the cunner is presented in Figure G.4.2-30. 1 In-Plant Effects. An extensive analysis predicting the ef f ects of entrainment losses on the local cunner population ms conducted by Stone and Webster Engineering Corporation (1976). The model utilized by S&W in their predictions was a density-independent eigen 4 value model which incorporates a Leslie population projection matrix. The biological interpretation of the eigen value is the finite populatio n g rowt h rate. (' In their analysis, S&W assumed an annual entrainment rate of 8.07 x 109 eggs and 4 7 x 108larvae. The small dif ferences between S&W's entrainment rates and those presented in Table.G.'4.1-2 result f rom S&W's use of the Simpson rule for numerical integration 2 and Applicant's use of the trapezoid rule. In their model, S&W predicted that ! entrainment would result in-an annual population reduction rate of .0008. The very conservative assumption was then made that this species has no density dependent 4 . compensatory mechanism and the loss rate was applied additively for each of the yars that NEP 1 and 2 operated. It ws also assumed that all Labrid-Limanda eggs were cunner. If the egg ratios of the three species involved have the same ratio as their larvae, then only 72% of the eggs are cunner (Table G.2.2-8). Under these conditions, the net ef fect af ter 40 years of continuous operation at 100% load (approximately 80% load is expected) would be a 3 03% reduction in the population size. Considering the conservatism built into the model, it must be concluded that the ef fects of entrcinment of cunner ichthyoplankton into the NEP 1 and 2 cooling water system will be negligible. G.4-57 1
_ _ _ _ _ _ . - . _ _m . _ _ _ . . . . - _ m .__ _ ____. . NEP 1&2 1 (
- Total Impacts. He cunner is a species which may be regularly entrapped in small numbers i .
l and entrained in fairly large numbers. We small number of adults lost will not be i likely to significantly af fect the large ubiquitous population. A mathematical model developed by Stone and Webster Engineering Company conservatively predicted a loss rate l of adults due to ichthyoplankton entrainment. This model predicts that the affected i population will be reduced in sire by a factor of 0.08% during one year assuming no l l population compensatory mechanism. It is important to emphasize that the 0.08% annual j population size reduction is a very conservative upper limit, because without density ! dependent coopensatory mechanisms . extinction is inevitable in all sp~ecies. Additional conservatisms built into this model are (1) the assumption that all Labrid-Limanda eggs ] l are cunner, and (2) the plant will always operate at 100% load. L i 4 j The analysis of thermal tolerance information indicates that temperatures expected in ) 4 the thermal plume will not adversely af fect the cunner. 1 l Applicant believes that the cunner population will not be subjected to appreciable harm ! by the operation of NEP 1 and 2's cooling water system. 1. ! 4.2.8 Sand Lance (Aamodytes americanus) l 4.2.8.1 Life History. The genus Ammodytes is a circumpolar and, at least in the ! Atlantic, the taxonomy is uncertain. It appears that the European species, E tobianus. t is a distinct species, however, there is such great similarity in the western Atlantic species A. americanus and A. dubius, and the European species & marinus that all three may in fac t, simply be races of one species (Reay,1975). It, therefore, seems reasonable to consider the biology of these other " species" since little deta'iled work has been conducted on h americanus. The American sand lance (h americanus) is found - along the North American Atlantic coast from Cape llatteras to the Gulf of St. Lawrence and may be found as f ar north as liudson Bay (Bigelow and Schroeder, 1953). G.4-58
NEP 1&2 The principle economic importance of & americanus in New England is indirect. They are a major bait or forage species for a variety ot predators such as cod, mac ke r e L , silver hake, striped bass and blue fish. Whales and porpoises consume great numbers of them (Bigelow and Schroeder, 1953) as do various seabirds, notably the terns which nest along our coast. In Europe, sand lance, primarily h marinus are marke ted f o r human consumption, and a similar fishery is under study by the National Marine Fishery Se rvice (R. Livingstone, Personal Communication) . Initially, such a fishery would probably focus on the larger, of fshore species, & dubius. Sand lance are generally found associated with clean sand or fine gravel substrates, and avoid rocky, muddy or coarse gravel bottoms. Kuhlmann and Karst (1967) studied the behavior of & tobianus in inshore waters of the Baltic. They observed fish emerging f rom the sand in small groups at dawn. These groups then merged to form large schools ( in excess of 1000 individuals which swam approximately 1000 meters to the sea-grass feeding grounds. The school returned to the sandy habitat around mid-day and spent the afternoon close inshore. Sand lance do not have teeth and are planktivorous. Richards (1963) observed that 10 species of pelagic crustaceans comprised most of the diet of Long Island Sound A. americanus. Ilis findings are consistent with those of Cov111 (1959) who described the food of post-larvae from the same area. Most & marinus become sexually mature at age two and essentially all individuals are mature at age three. Hacer (1966) repo rted tha t .5%, 80%, and 98% spawned at the respective ages of one, two and three. Ammodytes americanus spawns in the winter and early spring. The eggs are demersal and adhesive, innd the larvae occur in Block Island Sound from Decanber through mid June (Figure G.4.2-31). Larvae are more plentiful nearshore (Figures G.4 2-32 and G. 4 2-33), and are found G.4-59
. . ~ - _ - . . _ - .._.
NEP 1&2 thrcughout' the water column (Norcross et al., 1961). The oldest reported age of h ( americanus is 9 years (Macer, 1966). , Applicant obtained length and weights from a random sample of 155 adult h americanus (61 females, 94 males) obtained in Newburyport, Massachusetts during the month of October (just prior to the spawning season) . The length-weight regression equation for this cpecies was We igh t (g) = 0.0697 Length (cm)1.7152 Th3 averge weight of the sample was 5.05 g, and the average length was 12.15 cm. Scott i
- (1968) reported that the average length of & americanus he collected in Newburyport ,
was 12.7 cm. I .
; 4.2.8.2 Impacts of Construction. Adult sand lance are ~ suf ficiently mobile to avoid l ~
( the construction area, and the large amount of time speht in the sand implies that they f are cepable of tolerating highly turbid conditions and shoul'd not be harmed by any ,
- turbidity increase. Because the eggs are demersal and adhesive, those few which may bs in the construction area will' be lost. It is also expected that a comparatively ccall number of larvae will be affected. Under these circumstances, no appreciable harm to this species is anticipat.ed as a result of construction.'.
! 4.2.8 3 Impacts of Plant Operation.
i
^
En trepmen t. The potential for sand lance entrapment is judged to be low to medium and ]
~
10 cxpected to be highly seasonal. j . Fishery statistics indicate that the sand lance is highly seasonal in its susceptability l 4 to capture. Data presented by Reay (1975) indicates that virtually the entire North 4 ( Sea catch takes place from April through August. The liter ture generally supports tha (navailability of free-swimming . sand lance during the winter months and yet Macer
$ G.4-60
. .i
.-_m.._, _ . _ _ . _ - _ . - ,,_...-y . - . . . , . . _- .y. , , . _ . ,,___m,.,.,%y._ ._m4r,.. , ._,_,-,.r,_. r._. ..
NEP 1&2 (1966), and Cameron (1958) were able to obtain some specimens year round. In spite of i their absence.from the catch, the presence of larvae in the winter adequa tely desonstrates that adults are present even though they may spend little time in the water
-column. Winslade (1974) concluded that & marinus spent most of the time from August through April buried in the sand. As a result of the above plus the diurnal patterns described by Kuhlmann and Karst (1967), and Winslade (1974) it is believed that the sand lance will only be a potential candidate for entrapment during daylight hours of the warm months.
Kuhlmann and Karst (1967) estimated that & tobiunus usually swam at a speed of 30 cm/sec (roughly 1 fps), and that they were capable of short escape bursts to speeds of 300-500 on/sec (9 82-16.37 f ps) . Wyllie et al. (1976) determined that the critical swimming speed (essentially a predicted sustained swimming speed) for one 13 3 cm Ammodytes sp. f rom.a New Jersey estuary (therefore, probably h americanus ) was 0.93 f ps. It is ( 'herefore, evident that the burst swim speed of the. sand lance should easily permit t this fish to escape the 1.5 f ps velocity a t the l'ip o f t he p ropo sed intake. Due to the burst swimming speed, the short period of time during which the sand lance will be subjected to entrapment and its performance for water over unobstructed sand bottoms and its failure to be attached to reef-like structures, it is expected that t this species will only be impinged occasionally. The r ef o re, there will be no appreciable harm to the local population of sand lance as a result of NEP 1 and 2's operation. Within the Discharge Plume. As a result of their investigation of sand lance larvae alorg the inner continental shelf wters of f lowe r Chesapeake Bay, Norcross et al. (1961) theorized that spawning takes place before bottom temperatures reach 9 C (486 p), Since the eggs are demersal and adhesive, the possibility exists for a portion of the ( discharge plume to interact with sand lance eggs. If a worst case analysis were made G.4-61
NEP 1&2 whereby sand ' lance eggs were assumed intolerant of a 6 F temperature rise then approximately two bottom acres could be af fected. Inasmuch as the area that could be affected is small relative to other sand lance spawning sites, any associated impact is considered inconsequential as a result. Applicant collected sand lance larvae in Block Island Sound from mid-December through aid-June (Figure G.4.2-31) . Water temperature profiles during the last collection containing sand lance larvae were 9 9 C bottom to 14.10C surface on June. 4,1975 and 0 12.2 C bottom to 14.0 C surface.on June 17, 1976. It is, therefore,, certain that Block Island Sound sand lance larvae are naturally found in water whose temperature, exceeds 12.20C (54.00 F). On the warmer of these two days (June 17, 1976) the integrated water. temperature (bottom to surface) at the sample (and intake) location was 13 200 (55.8 F) . If for the sake of conservatima, it is assumed that any larvae subjected to temperatures greater than 13 20C will not survive, then a worst case analysis of the ( effsets of the 6 F 0temperature rise may be made. Six degrees Fahrenheit less than 13.2 C is '9 9 C (49 8 F) . Based on surf ace wa ter temparatures at the time of actual collections, Applicant calculates that 99 71 and 99.8% respectively of the 1975 and 1976 sand lance would have metamorphosed prior to thm " critical" value of 9 9 0C. In view of this fact and considering the small area involved (i.e., <1 surface acre) and conservatism in the calculation, it is believed that sand lance population will not be adversely affected by the surface discharge plume.
. . o Adult.s, of course, are able to choose their own temperature preferenda and will not .
9 rctide in the plume .if the water is too warm. u I In-Flant Effects. Because A. americanus has demersal adhesive eggs, entrainment will not af fect this life stage. Sand' lance larvae, on the other hand, were present at the
~
1 '
- locction of the proposed inlet for an estimated 194 days in the winter of 1974-75 and I
1 C.4-625
NEP 1&2 218 days during .the winter of 1975-76. 'Ihe estimated number of larvae which would have 8 7 been entrained during these two years is 1 763 x 10 and 4.577 x 10 respectively if 100% plant load' is assumed.
'Ihe thiversity of Rhode Island, Mirine Experiment Station is currently conducting studies on the- biology of Ammodytes americanus for Applicant. Fecundity is being determined by counting all eggs f rom fish captured in October from Newburyport, ha ssac h us e t t s .
Calculations on counts from ten feciales ranging in total length from 10.8 to 15.6 cm has resulted in the following length fecundity regression equation: Fecundity - -15098.34 + 1629.56 (Length, cm) Within this size range, the data appears linear ; the r 2 of the data set'was 0.81.
'Ihe above regression was then applied to the total lengths of 61 randomly selected female
( sand ' lance in order to estimate the fecundity of the " average" individual. From this analysis, it was determined that the average female is 11 86 + 1.11 cm total leng th' and has a fecundity of 4232. In spite of the fact that sand lance live for many years, App'licant will conservatively assume fo r this analysis that they spawn only once.
- Ihe model utilized to analyze the eifects of entrainment was previously described in Section 4.1 2.2. Briefly, this model assumes that, on the average, a female will produce only two of fspring which reach the age of reproduction.
As an estimate for the survivorship' of sand lance eggs (S,) is not available, a series of analyses will be presented based on S, values of 0.01 and 0 50, the true value probably falls somewhere between these two and closer to the high value. From these values, the survivorship expectation of a given larvae (S t) may be calculated with the equation. ( G.4-63
i NEP 162 ( 2_ S1-(Fecundity) (S,) h us, d en S, - 0.01, St = 0.047 and when Se = 0.50, St = 0.00095 The projected number - of cdults Wich may be lost as a result of entrainment is calculated by multiplying Sg times the entrainment estimate. We predicted losses of adults is described by the following matrix: 1974-75 1975-76 0.01' 8.286 x 106 2.151 x 106 S, 0.50 167,485 I 43,481 , hus, th6 annual estimate of adults Icst as a result of entrainment falls somewhere r ( bstween 43,000 and 8,300,000 per year. E. It is also possible to back calculate the e sivalent number of females,whose spawn would ba lost as.a result of entrainment by dividing the numbers in the above matrix by two. Hun, the spawn of between 22,000 'and 4,150,000 females is expected to be lost to cntrcinment.
- r Utilizing the length-weight equation presented 'in the life history section, it is calculated th'at. tha. average' reproductive female. sand lance weighs approximately. 4. 8 gram 3 R us , 4,150,000 females would weight 19,920 kg while 8,300,000 lost adults
. (cvarage weight 5.05 'g) would weigh 41,915 kg. To put this upper limit of weight lost to the population in perspective, these numbers may be compared to the catch of the Eurapsan sand lance fishery. I
!? G. 4-64 ,
NEP 1&2 Bertelsen and Popp Kidsen (1958) reported that the average peak catches for a 75 vessel North Sea fishing fleet during late May and early June wa s 2,500 kg per hour. The vessels averaged 10,000 kg/ day /km2 Macer and Burd (1970) referenced catch rates up to 15,000 kg/ hour. Compared to catch rates like these and considering the great conservatism in the calculations, the effect of NEP 1&2 must certainly be viewed as very small. Total Impacts. Some sand lance eggs may be found in the vicinity of the construction activities in Block Island Sound; these eggs will be lost. Construction is, however, a mall area and short duration impact. Sand lance larvae are expected to be entrained ' f requently, however, based on the projected loss to the population, there will be no appreciable harm to the species. Likewise, the ef fect of the thermal discharge should be trivial because: 1) the eggs will not be present, 2) the larvae are thermally tolerant and 3) if they are not thermally tolerant, the adults are capable of leaving (if they even encounter the plume). Entrapment of this species is likely to be an infrequant event because of the amount of time the adults spend buried in the sand, their high burst swimming speed, and their preference for water over unobstructed sand bottoms and its failure to be attracted to reef-like structures. It is believed, therefore, that the operation of NEP 1 and 2's circulating water system will'. result in no appreciable harm to the sand lance population.' 4.2 9 Atlantic Ma~ckerel (Sember sembrus)
- 4. 2 9'.1 ' Li fe Hi sto ry. The Atlantic mackerel is a far-ranging species found on both s'. des of the Atlantic Ocean. On the western side of the Atlantic, its range extends
'f rom the Gulf of St. Lawrence to North Carolina (Bigelow and Schroeder,1953). It is oceanic rather than estuarine in habit and usually travels in dense schools anywhere f rom the surf ace to depths of 200 f athoms.
G.4-65
NEP 1&2 Mackarel become sexually mature when two years of age and an average female produces 360,000-450,000 eggs (Sette, 1943). , Fo r the 1932 year-class, Sette' (1943) estimated, that, for every million eggs laid, only four fish survived to an age of three months. Sette further estimated a total mortality rate of 0.0012 (0.12%) per day between the tgs of three months and three years. Acccrding to Sette (1943), the most important spawning area for this species is along ths coast of the southern New England and mid-Atlantic sta tes. Within this region
"..ethe area of densest distribution occupies about the inner half of the shelf off New Yo rk . . ." In 1973, mackerel spawning was most intensive in the area of Narragansett Bay during the third and fourth weeks of May (Marine Research, Inc.,1974). As noted in this report, spawning was most intensive near the mouth of the Bay, indicating the prafarence of this species for an oceanic habitat.
During 1974 and 1975, spawning .was intensive in Block Island Sound throughout the month ( o f. May (Figure G. 4. 2-3 4) . Few eggs and even fewer lervae were found in the Ninigret Pand collections; those that did occur in the Pond were found at.the sampling stations nacrsst the breachway. Larval abundance reached a peak in the Sound near mid-June in bsth years. . It was noted during 1975 that the concentration of both eggs and larvae incrzased in an of fshore direction; larval densities were found .to be significantly higher at sampling stations located well of fshore than at those located inshore (Figures G.4.2-35 through G.4.2-38) . Acestding to Bigelow and Schroeder (1953), mackerel average 22.8 cm (9 inches) in length of tsr one year, 27 9 cm (11 inchee) af ter two years, and 35.5 cm (14 inches) in length cftsr three years. The diet of post-larval mackerel includes pelagic amphipods, copspods , squid, launce, and pteropods (Sette, 1943), as well as molluscan larvae, (
' p31ychaete imrms, fish eggs, medusae and etenophores, and a variety of small fish G.4-66 -s
NEP 1&2 (Bigelow and Schroeder, 1953). In spite of the fact that mackerel are comparatively unimportant to the Rhode Island commercial fishery (approximately 1% of the total pounds and less than 11 of the total dollars in 1975), this species constitutes the largest single component of the ichthyoplankton in Block Island Sound (Tables G. 2.2-6, G. 2. 2-7 and G. 2 2-8) . Because of the susceptibility of ichthyoplankton to plant induced entrainment mortal L ty and the relative importance of mackeret to this component of the ichthyoplankton in Block Island Sound (Tables G. 2. 2-6, G.2.2-7 and G.2.2-8). Because of the susceptibility of ichthyoplankton to plant induced entrainment mortality and the relat'ive importance of i mackerel to this component of the environment, Applicant has had the effect of entrainment modeled by Stone and Webster Engineering Company. 4.2.9.2 Impacts of Construction. The mackerel is an of f sho re spawner whose ichthyoplankton decreases in abundance towards the shore (Figures G.4.2-35 through G.4.2-(,
- 38) . Because the adult mackerel tuve great mobility and can' avoid construction activity, and because the eggs and larvae are concentrated' of fshore, and considering the small area and sho rt time involved, no appreciable harm to the mackerel population is anticipated as a result of suspended sediments and turbidity caused by construc tion activity in Block Island Sound.
4.2.9 3 Impacts of Plant Operation Entrapment. Atlantic mackerel are potentially vulnerable to entrapment since they are a pelagic, migratory species and are 'found throughout the water column in inshore waters. a
*t. is not believed that Atla'ntic mackerel' are serious candidates for entrapment because of the followind reasons. Gill netting monthly f rom September 1974 'through March 1975 -
and commercial otter trawling twice monthly from April 1975 through March 1976 at the location of the proposed intake, both failed to ' catch a single Altantic mackerel. Since G. 4-6 7
NEF 1&2 thn otter trawl is not particularly selective for Atlantic mackerel, it is conceivable (~ that schools of mid-water mackerel went undetected. However, concurrent with each otter s trgwl set, echo soundings were made and at no time was a sizeable school ot mid-water fith observed. This evidence suggests that Atlantic mackerel do not regularly occur near the proposed intake and, hence, will not be f requen tly en trapped. Additionally, mackerel are an extremely fast and powerful swimmer and it is anticipated that they will be able to avoid or escape from the intake currents. According to Bigelow cnd Schroeder-(1953), mackerel less than one year old can sustain a speed of -six knots (10 fps) while circling inside a live car. Yearlings exhibited a sustained speed of 11.5 knots (19 fps) . In addition, Atlantic mackerel quickly become visually oriented. Also, the west coast ecological counterpart, the chub mackerel (Scomber _iaponicux) is rarely entrapped at coastal California power plants with velocity cap intakes. Since ~ substantial numbers of Atlantic mackerel are not expected to be entrapped, no i cignificant impact on the mackerel population is predicted.
- Within the Discharge Plume. The mackerel prefers relatively cold water, wintering along thn edge of the continental shelf at temperatures of approximately 7 C (44-450F) , and is seldan found in water with temperatures exceeding 20 C (68 F) (Bigelow and Schroeder, 1953).
Adult mackerel make their annual appearance in Block Island Sound from th'e month of U thy through- July - months with rapidly increasing water temperature (i.e., 46 F - 68 F) . Sptwning is most intensive in waters with temperatur.es ranging between 48 and 5 7 F (Sa t te , 1943 ).. Mackerel. eggs develop normally bets.en 52-700F (Bigelow and Schroeder, 1953). Altman and Dittmar (1966) cite the work of Moore (1940) who determined the upper
' tolcrance limit of the embryo 'of mackerel to be 69 8 F. By the time water temperatures g l l
rcach 7DOF in the warmer,t part of the surface plume (approximately July 1), the major G.4-68
NEP 162 spawning and larval life stages will have been concluded. In 1974, only 0.18% of the eggs and 147% of the larvae at Sta tion BIS A we re found after this da te. The . likelihood of an impact on this species as a result of Applicant's thermal plume is anticipated to be negligible when one considers the following: (1) the ability of the adult to select its preferential temperature as a result of its mobility, (2) the greater relative abundance of mackerel eggs and larvae further of fshore, (3) the small numbers of eggs and larvae which will be af fected, and (4) the short time frame during which these stages will be ef fected. Temperature data for the mackerel is presented on Figure G.4.2-39. In-Plant Effects. Mackerel represented the most abundant egg and larval components of the ichthyoplankton collected during Applicant's baseline studies (Tables G.2.2-6, G.2.2-7 and G.2.2-8). Consequently, a sophisticated mathematical model was developed (, in order to predict the effects of entrainment on this species (Stone and Webster,1976). The structure of the model is essentially that utilized by ICNAF (Lett et al. 1975). Stone and Webster made minor modifications to the model in order to allow flexibility in analyzing the effects of varying mortality rates and power station induced mortality. Input parameters include the population age distribution, age-specific 'mean weight, age-specific fishing mortality' rates, age-specific instantaneous natural mortality rates, age-specific growth rates, a density dependent stock-recruitment f unction, and entrainment mortality. The entralment mortality is a major source of conservatism 'in S&W s model. Entrainment mortality was overestimated because only the peak p'opulation egg and larval productions, as estir sted by the stock-recruitment function, were used to determine the percent of the spawn which was lost due to entrainment. If S&W had utilized the total annual production, the losses from entrainment mortality would have constituted a smaller f G.4-69 g
NEP 1&2 f raction of the population. l' A sensitivity analysis was conducted to determine (1) the ef fect of using various tortality rates and recruitment assumptions to estimate population size, (2) the ef feet of varying the various components of the stock-recruitment function, (3) the eifect of varying certain density-independent variables -(instantaneous natural mortality, instantaneous fishing mortality and age of recruitment), and (4) the effect of entrainment mortality. The model was run for a total of 80 years with and without the presence of NEP 1 and
- 2. The modeled population underwent fairly large oscillations in size both with and without entrainment mortality itu.luded. Depending on the selected input values fo r
. the various parameters in the. equations, this model conservatively predicts that af ter 40 years of continuous operation at 100% load (approximately 80% Ioad is expected) ,
NEP 1 and 2 will have caused a reduction in the mackerel population size of 0 9-3.4%. Thtse numbers represent 6.7 and 20.7 of the natural oscillstions predicted by inclusibn of the respective input parameters. A sensitivity analysis on the model demonstrated that population size changes of this magnitude could potentially be caused by rounding errors in the stock and recruitment function.
, Stone and Webster concluded that the model did not predict an effect of sufficient magnitude to disrupt the . normal p,attern of. the popula tion. While some effect was pradicted, the conservatism in the model tended to magnif y the effect. ,
T?tal Impacts. It has ,been demonstrated that ef fects on the mackerel population rGruiting from either thermal plume mortality o'r ' entrapment of' adults is negligible. P pulation reductions caused 'by entrainment of the egg's and larvae of mackerel
;cuperficially appear high (0.9-3 4% af ter 40 years offp lant operation at-100% load versus (
thm expected 80% load' factor) . However, when compared to natural fluctua tions and G.4-70'.
NEP 162 considering the conservatism S&W built into the model to ensure that the ef fects of the plant do not exceed the predicted value, these numbers a re indeed small. Applicant, therefore, concludes that the operation of NEP 1 and 2's cooling wa ter system will result in no appreciable harm to the mackerel population. 4.2.10 Butterfish (Peprilus triacanthus) 4.2.10.1 Life History. The butterfish is a relatively small (6-9 inch) fish that appears along the Rhode Island coast in the spring. According to Bigelow and Schroeder (1953), butterfish stay near the surface when inshore but are found 'at depths up to 115 f a thoms when o f f sho re. It is primarily a warm-wa ter fish and is found from Newfoundland to Florida. It is more abundant south of Cape Cod than to the north. Butterfish appear along the Rhode Island coast in April, probably having moved in from offshore (Bigelow and Schroeder,1953), and they depart the inshore waters by late fall. Horn (1970)-has separated Atlantic Coast butterfish into two distinct populations:
~
( an offshore, southern population that lives over mud bottoms and deep water and an inshore population, to which the Rhode Islan'd fish belong, that! extends all along the coast in shallower waters over sandy bottoms. Bigelow and Schroeder (1953), state that srawning takes place a few miles of f sho re. This was also observed in Block Island Sound during these studies -the largest concentrations of ichthyop1'ankton were found at the stations 2-4 miles offshore. Offshore, most of the spawning activity took place in June and July while the concentrati'ons of eggs 'and ' larvae were found lashore in July and Augu'st. ' Ca tc h da ta f rom a 45' stern trawler (Table G. 2. 3-3) suppo rts the thesis that the adults are. primarily found of fshore.- 'Ihe t'e mporal and spatial distribution of but'terfish eggs and larvae are presented in Figures G.4.2-40 through G.4.2-44. t As the summer progresses, young butterfish 'become plentiful in otter trawl-catches of f G.4-71 ,,
1 I NEP 1&2 Charlestown. According to Horn (1970), dif ferent size-classes of butterfish move independently during the summer months but move together offshore in deep water during-the colder part of the year. Young butterfish are regularly found in association with jellyfish medusae. Horn (1970) reports jellyfish to be the principal food of the juveniles until the fall of their first year, by which time they have reached a length of about 10'.cm (4 inches). Older fish continue to feed in part on medusae, but small fish, squid, crustacea, and worms by that time have become important components of the diet. Butterfish are a moderately valuable commetcial species in southern New England whose numbers have declined in recent years as a result of heavy foreign fishing pressure (Olsen and Stevenson, 1975). 4.2.10.2 Impact of Construction. Increases in suspended sediments and turbidity in ( the. immediate area of construction could adversely af fect eggs and larv'ae floating through the construction site. However, because of the wide distribution of this species and' its extensive spawning habitat, no significant effects are expected. The a'dult butterfish have sufficient mobility to avoid the construction site. Under these circumstances, no appreciable harm to the butterfish population is anticipated as a result.of construction. 4.2410.3'- Impacts of Plant Operation. Entrapment. The butterfish, since it 1.s a. coastal fish and not , restricted to a specific stratum, has a medium to high entrapment potential (CZC,1979). This an.trapment potential is ba' sed on the facts that (1) the butterfish' is largely planktivorous
~
(2) the ecologically .similar . species, Peorilus simillimus, is entrapped by velocity cap k intakes- in considerable numbers _in southern California despite its apparently low abun' dance there, and (3) it may be particularly susceptible.to entrapment during storm G.4-72' , i
NEP 162
'conditio ns. Entrapment of this species can be expected 'in May when immature, ' year-old i fish arrive in coastal waters, and again in early f all when young-of-the-year reach impingible size (CZC, 1979).
l Bere are, however, several factors which will tend to minimize entrapment of butterfish
- 4. at the proposed NEP 162 intake location. Chief among them include the fact that butterfish do not occur inshore near the site of the proposed in tak'e in particularly
]- large numbers as compared to their numbers of offshore waters. Sampling insho re by a commercial otter trawl, twice monthly, f rom April 1975 through March 1976, yielded 882 butterfish (Figure G. 2. 2-2) . Sampling at the of fshore location with the same gear and for the same . time span, yielded. 6,~428 butterfish. The location of the in take in } boulder-strewn area is therefore, not considered to be a preferred butterfish habitat. In addition, swim speed tests with butterfish have been perfonned by. Wyllie e t al . , (1976). Based on their data, the average critical swim speed for butterfish 3-3.5 inches
.( in length is 1.8 f ps which would allow this species to avoid or escape the in take s .
Furthermore, the species, with its short life span, has a history of sporatic population peaks and declines, as a result, in some years few will be available for entrapment.
~
Consequently, the potential for significant entrapment impacts is judged minimal. Within the Discharge Plume. The butterfish is a warm water species which migrates into New England waters during the warmer months of the year. Ic.. this area, they have been reported at temperatures ranging between 4.4 and 22.8 C (40 and 73 F) (Horn,1970; Fritz, 1965; Schaef'er, 1967). Colton (1972) reported a minimum spawning temperature of 15 C 0 (59 F) . The eggs are buoyant anil hatch in less than 48 hours at a temperature of 65 F. f They probably will not develop unless the wa ter is comparatively warm. The later statement is supported by the fact that Bigelow.and Schroeder (1953) have taken a A considerable number of eggs but only two larvae north of Cape Cod. As with other species which migrate from the south, it is reasonable to assume that G.4-73
. _ . . _ _=
d NEP 1&2 F butterfish have a tolerance or even a preference for relatively warm temperat'ures. I ha informatio'n presented by B'igelow and Schroeder (1953) certainly suggests that the aggs and larvae will not be adversely af fected by a temperature of 6 F above ambient. We adults should certainly not be af fected by the plume as they may avoid it in the event it is stressful. In-Plant Effects. Butterfish eggs occurred for 154 days and 107 days, respectively, during 1974 and 1975. he larvae occurred for 105 and 76 days during the same respective periods. If NEP 1 and 2 had operated at full load during this period and assuming that the ichthyoplankton are uniformly distributed throughout the water column ( the eggs hava an oil globule and are buoyant), then 2.832 x 10 7 eggs and 6.621 x 106 larvae would have been entrained in 1974, and 8.889 x 10 7 eggs and 1876 x 107 lartae, in 1975. I Thz entrainment of eggs and larvae can be equilibrated to the number of sexually mature fish that would have developed from the entrained forms in the same manner as described in Section 4.1.2.2. Le fecundity and survivorship of the butterfish is not documented and, therefore, an estimate of the fecundity is necessary. The fecundity of the butterfish is estimated by asstating that the volume of each ovary is approximately two cubic centimeters. Since thidiameter of a butterfish egg is approximately 0.7 to 0.8 millimeters (Bigelow and Schroeder,1953), it is conservatively assumed. that each egg occupies one cubic nillimeter of space in the ovary. he fecundity of an average butterfisn is, therefore, predicted to be 4,000. his fecundity appears drastically small for a species with pslegic eggs, when compared to other species,.and is considered conservative. A 4 he average . spawning ' life of the butterfish is also not documented and is, therefore, conrervatively assumed to be c 1e year. During its breeding life, it is, the ref o re, , predicted that the avera'g'e butterfish will lay 4,000 eggs. a G.4-74
NEP 1&2 t The incubation' period for butterfish eggs is a relatively short 48 hours (Bigelow and Schroeder,1953), and, therefore, the egg to larval' ratio is assumed to be a measure of the egg r larval survivorship. The average egg to larval ratio for all Block Island Sound. Stations for 1974 and 1975 is 3 to 1, while the average egg to larval ratio at Station A is 4.5 to 1. The best estimator of the actual egg to larval ratio is based on the maximum nur'er of samples. However, since the higher egg to larval ratio adds conservatism, it will be used. The larval entrainment in 1974 and 1975 is, therefore, equivalent to 2.98 x 107 and F.44 x 10 7 eggs, respectively. Based on the calculated egg and larval entrainment and the assumed fecundity and spawning life, the operation of NEP 1 and 2 would have resulted in a loss of 29,000 and 86,700 butterfish in 1974 and 1975, respectively. According to Bigelow and Schroeder (1953) butterfish average six to nine inches in length ( and weigh approximately f our ounces. Ba sed on this we ight , the lcus due to the entrainment of eggs and larvae is equivalent to 7,250 and 21,680 pounds of butterfish for 1974 and 1975, respectively. The Rhode Island commercial butterfish landing in 1975 was 1,899,000 pounds. The average commercial butterfish landing for the years 1971,1973 and 1975 was 1,433,000 pounds. Since the smaller number adds to the conservatism, it will be used. The loss due to the entrainment of eggs and larvae in 1974 and 1975 is, therefore, equivalent to 0.5% and 1.5% of the average commercial butterfish landing. Considering the great conservatism built into the above . calculations, it is concluded that the entrainment .of butterfish eggs and larvae by NEP 1 and 2 will result in no appreciable harm to the population. Total Impacts. Utilizing very conservative techniques, it can be concluded that the G.4-75
1
. i NEP 1&2 combined impact of entrainment and entrapment on this species will be in the range of 1-2% of the Rhode Island commercial landings. If the true impact could be calculated,,
it would very likely be equivalent to a fractional portion of 1% of these landings. No. impact is expected as a result of thermal effects within the discharge plume. It is, therefore, concluded tha t no appreciable harm will result on this species resulting f rom the operation of NEP 1 and 2's cooling water system. 4.2.11 Winter' Flounder (Pseudopleuronectes americanus) 4.2.11.1 Life History. The winter flounder is a species of consid'erable impo rtance to both the commercial and recreational fisheries of New England. It is a benthic fish that is found in large numbers in the inshore area and is taken in commercial quantities from Nova Scotia .to New Jersey, although its range reportedly extends from Lab rador to Georgia (Bigelow and Schroeder,1953). ( Areas of maximum abundance are Nantucket Shoals, Georges Bank, Gulf. of Maine and Cape Cod Bay, Block Island Sound, and long Island Sound. Members of the of fshore populations, often referred to as " lemon sole", tend to attain c larger size than do those from inthore. They attain lengtlis up to 60 cm (25 inches). The inshore populations of winter flounder - of ten referred to as "blackbacks" in the Ecre southerly portions of their range - are generally found in depths of 1 to 30 fathoms. These fish seldom exceed 50 cm (20 inches) in length. Although occasional , pattern of movement seems to be that of inshore-offshore migrations in response to temperature (Perlmutter,1947; Saila,.1961) . ;According t_o McCracken (19.63)',12 to ISOC (54 to 59 F) is the preferred temperature range.
~
Winter flounder range from the Gulf of St. Lawrence to the Chesapeake Bay in substantial numbers and inf requently as far south as Georgia (Bige1.;w .nd Schroeder, 1953). Adult. G. 4- 76
i NEP 1&2 winter flounder feed on small shrimp, amphipods, ascidians, seaworms, bivalves, squid, holothurians and hydroids (Bigelow and Schroeder,1953). Winter flounder become sexually mature when two to three years of age. Typically, adult fish move shoreward in the fall to spawn in relative shoal bays, inlets and estuaries (Sa ila , 1961; Jef f ries and Johnson, 1974). Spawning in southern New England wa ters usually occurs during mid to late winter. Unlike most other species of flatfish, the eggs of the winter flounder are both adhesive and demersal. Hatching of the eggs south of Cape Cod may occur in February, reaching a peak during March and early Apr it; in the colder wa ters north of Cape Cod, hatching may be at a maximum in early May. Pearcy (1962) described the larval flounder as nonbuoyant and . as displaying a mixed 1 planktonic-benthonic behavior. Older larvae characteristically are found in greater abundance near the bottom than are the younger forms, and their ability to st ratif y _ 1 enhances the likelihood of their being retained within an estuarine system even though the net water flow is seaward. At metamorphosis, which may occur two months or so af ter ha tching , the left eye of the little flounder moves over the right side of the head as it assumes its flattened shape, giving its r igh t-handed a ppe a r ance. he winter flounder is a species of considerable importance to both the commercial and recreational fisheries of New England. It is taken in commercial quantities from Nova Scotia to New Jersey. During the years 1971-1975, the annual commercial landings of winter flounder in Rhode Island have averaged around 4 million pounds, he value of the 1973 Rhode Island commercial catch was $877,000 (01sen and Stevenson, 1975). It has been estimated (Deuel and Clark,1968) that approximately 26 million pounds of flounder are caught by sport fishermen in southern New England each year. he high percentage of tagged fish recaptured in the area of release, in conjunction i with information on spawning behavior and early life history (see below), led Perlmutter i 1 G.4-77
. . ~ - _ _ _ _ _ _ _ . _ _ _ ,_ ___. _ _ __ _ _ . _ _ _ . , _ __ . _ _ _ _ _ _ _ _ _ _ _ _
NEP 1&2 l I (1947) to conclude, that in southern New England at least, "... young blackback flounders cre the product of local spawning..." and ".. . stock of adult fish drawn upon by the sport and commercial fisheries remain highly localized...". Because winter flounder were common in both the ichthyoplankton and trawl samples, and because Ninigret Bond, like the other salt ponds on the Rhode Island coast, is a nursery area for this species, Applicant has had the effect of entrainment modeled by Stone and Webster Engineering Corporation (1976). l The temporal and spatial distribution of winter flounder eggs and larvae are presented in Figures G. 4. 2-4 5 through G. 4. 2-4 7. 4.2.11.2 Impacts of Construction. Adult winter flounder have suf ficient. mobility to avoid the construction area and the larvae are present in such relatively low numbers i, (compared to Ninigret Pond) that no appreciable . harm is anticipated as a result of short t rm construction activities.
~
4.2.11.3 Impacts of Plant Operation Entrapment. The winter flounder, because of its af finity for the bottom and because of the protruding lip of the velocity cap intake, is not expected to be vulnerable to Gntrapment. Suppo rt for this judgement.can be devised from the California velocity cap experience with the discad turbot (assumingly close ecological eqdivalent to winter flounder) which has shown that even the original velocity cap designs are ef fective in minimizing entrapment of benthic . flatfish (CZC, 1979).
~
Add'itio'nally, winter flounder do not congregate 'in large concentrations near the location of the proposed intake. TVice monthly o.tter trawling f rom April 1975 through March 1976 (Figure C.2 2-1) produced only 125 fish inshore. Otter trawling of fshore during
~
thm same period netted 1,393 fish. The proposed intake locations is, therefore, not G.4-78
NEP 1&2 4 considered to be prime habitat for winter flounder. Swim speed tests with winter flounder have been performed by Wyllie et al . , (1976). Utilizing their data, the average critical swim speed for flounder 3.5-7 9 inches in length has calculated to be 1.5-1.6 f ps. Furthermore, the endurance of winter flounder was investigated by Beamish (1966). lie found that wintet flounder 7.4-9 1 inches in length could endure velocities of 2.5 and 4.4 f ps for periods up to approximately 25 and 5 minutes, respectively. Consequently, it appears that winter flounder could escape or avoid the NEP 1 and 2 intakes. Due to the low densities of winter flounder near the in take location and the bottom dwelling nature and swimming speed capability of the species, the entrapment of winter flounder is not expected to occur f r eque n tly. The refo re , no appreciable harm on the winter flounder population is expected.
~
Within the Discharge Plume. Much has been written concernin'g. the temperature tolerance of the juvenile and adult life history stages of winter flounder. Winter flounder become sexually mature at two to three years of age, with spawning taking place during winter and early spring. Thompson et al ., (1971) reported that incubation takes 15-18 days at a temperature of 37-38 F. ! Hoff and Wesunan (1966) conducted temperature rolerance tests on 8.6-11.3 cm juveniles. When acclimated at 7, 14, 21 and 28 0 C (44, 57, 69 8 and 72 0 F) and tested at the respective temperatures of 20, 23, 26 and 29 C (68, 73, 78.8 and 84.2 F) for one hour, no mortality was observed. i-Huntsman and Sparks (1924) subjected P., americanus adults to tests in which temperatures were increased at the rate of 1 C per five minutes until they succumbed. The incipient lethal temperatures for this demersal species was found to range between 822-871 i 0 F. Testing the adult stage, McCracken (1963) describes their ability to orient to G.4-79
NEP l&2-certain isotherms during seasonal migratory movements. From this investigation, he postulated an upper incipient lethal temperature of 27 C (80.6 F) . ' Gif t and Westman (1971) in their study increased water temperatures from an initial acclimation temperature of 680F by 0.6 i 0.1 F/hr until 8012 F was reached. Hereafter, the temperature was raised 2.5 F i 0.5 F/hr until avoidance response and avoidance breakdown temperatures were realized (avoidance breakdown is defined in Mihursky and Kennedy, (1967) as CIM or critical thermal maximum) . he results of their } - study indicate initial avoidance behavior for one year olds at 75.5 F with an avoidance breakdown at 870F. The authors go on to cite an upper thermal tolerance limit for one , ysar olds at 88.3-89.170F. Again, it is necessary to point out that due to the nature of their experimental method, the upper tolerance limits presente'd in Gif t and Westman's investigation do not provide indications of exact lethal temperatures, but rather provide a measurement of the relative thermal tolerance of the winter flounder. Meldria and Gif t (1971) give a discrete preference temperature o'f 67 F when the adult is acclimated ' } at 10 F less (i.e., 57 F). Frame (1973) describes a growth temperature range for one yaar old flounder between 53.6 and 60 F. From the standpoint of plant operation, possible impact to this representative demersal apecies as a result of an induced 6 F temperature rise is expected to be insignificant. Such a position is based on several factors. i
- a. he eggs of this species are demersal and adhesive, with the majority of spawning i taking place in coastal salt ponds such as Ninigret Pond. Therefore, the probability of this life history stage being involved with the thermal discharge or being af fected by a design surface maximum within the boundary of the mixing
, zone is relatively small. 4
- b. he literature demonstrates rather conclusively that the juveniles can tolerate l
i G.4-80
-, _ -- .-_ ., - - .. . - - . ~ - - .. . _ - - - . . - - - - - .
NEP 162 water temperatures well in excess of those anticipated'once the plant is 4 operational.. Temperature tolerance limits for periods Wien juveniles are known to occur at the site (i.e., winter and spring) exceed the projected surf ace n.aximum temperature by anyWiere from 3 to 180F. d
- c. As presented in Figure G.4.2-48, adult flounder are found throughout most of the year at the proposed site. Of particular relevance is tha t a maj ority of the temperatures from temperature tolerance studies conducted coincide quite closely with the warmest water temperatures that the adult would experience dur ing the month of August. In all instances, the upper thermal tolerance limits exceed the anticipated surface maximum of 76 F that would be experienced within the boundary of the mixing zone. Impacts as a result of thermal stress are, the re f o re , not an ticipa ted . Irrespective of this species' temperature tolerances, it must be kept in mind that we are dealing with a demersal species which, in all likelihood, will have minimal interface with the thermal discharge.
In-Plant Ef fects. The vinter flounder is the only one of the representative important species discussed in this document which is believed to have a nearby and relatively important nursery area. Th is a r ea is the Ninigret/ Green-Hill Pond complex. The mathematical model which Stone and Webster (1976) used to predict the effects of a entrainment on the winter flounder is a self-regenerating dynamic pool model originally developed by Hess, Sissenwine and Saila (1975). It incorporates a density-dependent stock and recruitment function which predicts age 1 recruits from the previous year's spawn. Input values include estimates of age-specific fecundity for each of the 12 year classes, natural and fishing mortality, survival from egg to age 1, standing crop and entrainment mortality. The model only addresses the ef fect of entrainment on the Ninigret Pond population and does not consider the populations remote from the site.
~
4 In their analysis, Stone and Webster conservatively predicted that 1.5% of the original G.4-81
NEP 162 larvae produced in Ninigret Pond would be entrained. The conservatisms in this ( prediction and its subsequent impact a ssessmen t include the following assumptions: s
- a. The larvae are rand omly d is t r ibu ted throughout the wa te r column ;
- b. The entire Pond is un i f o rmly remixed on each tidal cycle;
- c. The plant will operate continuously at 100% load; and
- d. No larvae are in - the " ambient" wa ter of Block Island Sound , i .e . , larvae from other sources do not metamorphose in Ninigret Po nd .
The assumption that the larvae are randomly distributed throughout the wa te r column is contrary to the findings of other investigators. Howe '(1974) found that larvae were eleven times more abundant in the bottom wa ter than in the near surf ace wa ters of Nantucket Sound. Pearcy (1962) reported that in the Mystic River estuary (Connecticut) - ( winter flounder larvae were about six times as abundant near the bottom as they were n::ar the surface. In that estuary, this distributional pattern resulted in an estimated lors rate less than one third of that which would have been expected had the larvae been randomly distributed. The ef fect. of uniform mixing of the Pond's wa ter on each tidal cycle is certainly conservative and not supported by any evidence. Raytheon Company (1975) reported that crrrents in the Pond were dominated' by local winds and that flushing of 'the western b Oin was irregular. Fu r the rmo re, f rom Figures G. 4. 2-4 6 and G. 4.2-4 7, i t .is ~ obvious that the larvae are found in greater concentrations at points distant from the breachway .- a cituation not. possible. mder the asstanption share. The assumption of 100% load is obviously conservative when the 40 year plant ' life is considered . This number will probably be on the order of 80%. G.4-82
NEP ,1&2
- The assumption that -larvae f rom other sources do not have an opportunity to contribute to the population of Ninip .et Po nd is clearly conservative. During'1975 and 1976, Applicant observed that. depending on the year and station, larvae were present in Block Island Sound for one or two months af ter they were no longer present in productive areas of the Pond. Ihrthermore, data from Station BIS-P (Figure C.2.2-1) clearly demonstrates that larvae are arriving in the study area fran other sources.
A fifth asstanption, which is very likely conservative, is that all of tl'a larvae flushed from the Pond have the same probability of survival and subsequent rec rui tmen t into the local population as those which remain in the Pond. Pearcy (1962) states " Larval
. mortality in of fshore waters is thought to be higher than that in the estuary." Lawrence (1975) reported that winter flounder larvae required 49 days to metamorphose. at 8C and 80 days, at 5 C, only three degrees lower. Larvae did not survive to metamorphose when held at 2 C. 'Ihe importance of this data is apparent when it is correlated with
( the ambient water temperatures during the presence of the larvae and witti life table a statistics before and af ter metamorphosis. During the months of April and May 1974 and 1975, when winter floundar larvae were most abundant in Block Island Sound , the water in Ninigret Pond was on the order of 5-6 C warmer than it was in the Sound. Saila (1976) utilizing information presented by Pearcy (1962) developed a mathematical model which maintained a stable population through time. This life table, along with Z values (instantaneous mortality rate) is presented below: M Survivorship Z/ Day Larvae Hatch to 26 days 0.004536 0 2075 27-60 days 0 2995 0 0355 C.4-83 l
l NEP l&2 ( Juvenile 3-12 months 0.03546 0.0109 12-24 months 0.3491 0.0029 Subsequent years 0.33 0.0030 From this table, it can be seen that the instantaneous mortality rate is more than 3 tines as high for second semester larvae as it is for juveniles. It is, there f o re , of definite survival advantage to metamorphose as early as possible. Since it is 5-6 C warmer in the Pond than in the Sound, it is reasonable to conclude., based - on Lawrence's info rmation, that something greater than an extra month is required f or natamorphosis in the Sound . As previously noted, the thesis of prolonged larval - retention in the Sound is circumstantially supported from field data: the larvae are collected for an extra 1-2 months in the Sound. Winter flounder apparently metamorphose at one of the smallest sizes for pleuronectids (Bigelow and Welsh, 1925; and Kyle, 1898; as referenced in Pearcy,1962). Demere 1 adhesive eggs, early metamorphosis, and a benthic preference all increase the probability of larval retention within an estuary. These adaptations have been " selected-for" in the life cycle of the winter flounder presumably because of their value in increasing curvival. It, therefore, seems reasonable to postulate that larvae which are flushed from Ninigret Pond have a lower survival rate than those retained within the nursery srca. With these five conservative assumptions in their model, Stone and Webster predicted that 5.4 x 106 larv'ae would be entrained from Ninigret . Pond's 1975 larval population. Over a period of 40 years, they predict that the 0.015 entrainment mortality rate would resul t in a decrease in the population of Ninigret Pond 'of about 9%. A sensitivity enclysis was applied to the various parameters of the stock and recruitment f unc tion, G.4-84
NEP 1&2 age-specific fecundity, and age-specific survival. This analysis revealed that the 4 i predicted population size decrease is less than might be expected from a 10% change in the most sensitive of the model parameters. Considering the highly conservative assumptions inherent in their calcula tions, the fact that small errors in estimating the parameters could have produced this eifect,
'and the five fold variation in Rhode Island wiriter flounder landings (Stone and Webster, 1976, Figure 8. 5-2 ), it seems unlikely that operation of NEP 1 and 2's cooling water system will result in a measurable change in the size of this population.
During 1975, Applicant predicted that if the plant had operated at full load, 4.577 j x 108 larvae would have been entrained (Table G.4.1-2). If we assume that Stone and Webster's predictions of larval density as a result of flushing f rom Ninigret Pond are i not conservative, but realistic, then their estimated 5.4 x 106larvae would only account
.f. . for 1.2% of the larvae entrained by the plant. As larvae may originate from many sources .
(e.g., Narragansett Bay and the Niantic River), additional analysis is required, and l the subsequent discussion will address the effects of the entrainment of larvae from ! all sources. I-i
'Ihe survival curve for a cohort of winter flounder will follow the general equation:
4 N (1) t = Noe-Zt Miere Nt = number at time t No = number at time 0 Z = i'nstantaneous mortality rate i 1here will be a separate curve for each age group represented in the above survivorship table. As larvae are not frequently captured af ter age 53 days (Pearcy,1962), we can G.4-85
A NEP 1&2 calculate the survival curves for the larvae in our samples based on the first two lines / in the previously presented survivorship table. If it is assumed that, over a spawning season, the age f requency distribution of the
; entire larval population is equivalent to the age frequency distribution of the larvae that a given cohort experiences throughout its occurrence, then equation (1) defines
- the age frequency distribution of the population. If it is assumed that all age classes of the larval population which are 53 days old or younger are entrained at a rate commensurate with their relative abundance, then equation (1) also identifies the age f requency distribution of the entrained larvae. The number of larvae entrained (E)
- is then defined by the ecuation
E=N g e-0. 2075 t dt + N 26 e. 355 (t-26) dt (2) 2 . If it is assumed 'that 100,000 larvae per day enter the subpopulation which is destined to be totally entrained, then No= 100,000 and, from the survivorship table, N26 " 453.6.The solution to equation (2) then comes: E = 4 79,678.6 + 7881.3 - 487,559.9 (3) In this example, E represents that fraction of 5,300,000 larvae (53 days x 100,000 lcrvae/ day) which had survived until they were entrained. .It is., therefore, assumed { that. the number of larvae which are entrained by NEP'1 and 2 will represent approximately 9% of the production of some number of females (488,692.3 divided by 5,300,000). From Table G.4.1-2, Applicant estimates that if NEP 1 and 2 had operated at 100% load - during 1975, 4.577 x 108 winter flounder larvae would have been entrained. In order to entrain that many larvae, it would have been necessary for 5.086 x 109 eggs to hatch. ( i Assuming a hatching rate of 53% (average of 33-73% from Scott, 1929 as referenced in G.4-86 i
1 A NEP 1&2 Saila,1976), the 5.086 x 19 9hatching eggs represent, an initial spawning of 9.595 x
^
109eggs. Assuming a fecundity of 366,700 eggs for the average female of 348 grams I (Saila, 1961), the projected entrainment represents the spawn of 26,170 females which weigh a total of 20,070 pounds. Projecting the calculations forward instead of backwards, we find f rom the survivorship table that of the 5.086 x 109 eggs which hatched, only 28,226 age 3 adults (breeding age) will enter the population. Three year old winter flounder average 227.3 grams (lle ss , Sissenwine, and Saila, 1975). The projected loss, therefore, will weigh approximately 14,164 pounds. During the ' period from 1971 through 1975, the Rhode Island commercial winter flounder landings averaged 4,000,000 pounds (U.S.D.C.1974,1975 and 1976). The adults whose spawn is lost and the projected loss of three year olds, therefore, represents 0.50%
-{ and 0.35%, respectively, of the average -Rhode Island landings.
Because of the . low magnitude of. entrainment losses when compared to the Rhode Island landings, Applicant believes that the ef fected winter flounder populations will not suffer appreciable harm as a result of larval entrainment. Total Impacts. The winter flounder is a species which will not be entrapped with any great frequency. It is thermally tolerant and should no't be affected by r.he thermal plume. 'lhe eggs are deinersal adhesive and are, therefore, not subject to entrainment. Th e only potential for an impact will be from the entrainment of' larvae.
"Ihe larvae of winter. flounder are concentrated inside Ninigret Pond in densities which greatly exceed those found in Block Island Sound, and only an estimated 1.5% of the Pond's larvae will be entrained in the unlikely event that a series of very conservative asstamptions proved correct. Additionally, there is reason to believe that those larvae which are flushed from an estuary have a reduced probability of survival and any C.4-87 e
HEP 1&2 predicted entrainment ef fects wo'uld again be overestimated. Even if all of the ( conservative assumptions are true and the larvae in the Sound have an equal probability of survival, entrainment losses would equal a fractional percentage point of the Rhode Island commercial landings. , ConIequently, Applicant believes that the operation of the heat dissipation system of NEP 1 and 2 will not result in appreciable harm to the winter flounder population. 4.2.12 Blue M2ssel (Mytilus edulis) 4.2.12.1 Life Histo ry.' On the western side of the Atlantic, the' range of the blue mu;cel extends from polar regions southward to North Carolina (Miner,1950). Although it often occurs in greatest concentrations, and appears to grow best near the area of , thn low tide mark (Loosanof f and Engle, 1943), in areas of abundance it may be found both within and beyond the intertidal zone forming dense colonies on rocks, pilings, [ sand bars, and other sur f aces by a t tachmen t with its byssal threads. As is true of other bivalve mollusks, the mussel is a prolific spawner, capable' of reltasing many millions of eggs (Field,1922). . Spawning is usually triggered by rising temperatures. In Southern New England, the major spawning ef fort usually occurs in leta spring; however, the larvae have been observed in the. water column year round. The duration of the larval period is variable but is approximately 14 days (Loosancff rnd Davis, 1963). During this time, the planktonic larvae are essentially at the mercy of water currents and may be transported considerable distances from the' area where spawning occurred. The temporal and spat,ial distributions of Mytilus larvae are precented in Figures G.4.2-49 through . G.4.2-51.
~
The metamorphosing larva, or pediveliger, ma'y be quite selective in its choice of attachment, exploring the surface of the substrate by means of its foot and tentatively i attcching itself by means of its byssal threads. The ability to disengage itself from G.4-88
NEP 162 the substratum by severing the byssal threads, and to reattach at a new location by secreting additional threads, is retained throughout its life (Field, 1922). The growth rate of the mussel is variable, ' depending upon temperature, cur ren t, and other environmental factors. In areas favorable for growth, they may reach a size of 60-65 mm (2.5 inches) in one year (Davies, 1969). During the summer of 1974, juvenile mussels were found in abundance in Block Island Sound, forming dense colonies on the bottom. Heavy mussel sets were not observed at the same locations during the summer of 1975. Although of limited commercial value at the present time, the mussel is of significance as an important source of food for many species, most particularly the tautog (Tautoga onitis) and cunner (Tautogolabrus adspersus) (Bigelow and Schroeder,1953). Because of its tendency to form dense colonies and thereby cover or obstruct underwater objects ( such as cooling water intakes, the mussel may also become a serious pest in souie areas. The mussel is prized as a food item -throughout much of . Europe. However, it has failed to arouse much interest in the average American consumer and, therefore, does not command as high a market price as other bivalves such as oysters, clams and scallops. Because mussels can be cultured in exceptionally high concentrations to yield significant quantities of valuable protein (Bardach et al.,1972), interest in this species as a potential food source has been increased in this country in recent years. 4.2.12.2 Impacts of Construction. It is possible that the suspended sediments and turbidity' could adversely af feet mussel larvae passing through the construction site. Additionally, those mussels present in the construction area will be lost.as a result of dredging and overboard disposal of spoil. Although significant sets of juvenile
; mussels have occurred in Block Island Sound in the area of proposed construction, natural conditions are evidently unfavorable for musuei development and maturity: Applicant G.4-89
NEP 1&2 has found very few adults in the area. Under these circumstances, no appreciable harm { to the blue mussel popula tion is an ticipa ted as a result of construction. 4.2.12.3 Impacts of Plant Operation. Entrapment. With the exception of those mussels which are either killed or which release their byssal threads during backflushing operations, no mussels will be entrapped. Within the Discharge Plume. As a result of its importance as a biofouling organism of intake pipes at electric power plants, the thermal tolerance of the blue. mussel has received considerable attention. During Applicant's studies, dense concentration of juvenile mussels were found in Block Island Sound. As described earlier, this bivalve species is a prolific spawner, capable of releasing millions of eggs. Spawning usually occurs in late spring when water temperatures reach approximately 60 F. (Engle and loosanof f,1944). The duration of larval planktonic development is -approximately 14 days (Loosanof f and Divis, 1963). Lough (1974) reported optimal water temperatures for larval survival and growth between 11 and 140C (52-570F) at a salinity range of 22. 5-3 6. 5 o/oo. Brenko and Calabrese (1969), on the other hand, found more than 70% survival of Mytilus edulis larvae tested for 16 to 17 days at almost all salinities (15-40'o/oo) at temperatures renging f rom 5 to 200C (41-68 F). Erratic survival at 25 C (77 F) indicated that this temperature approached the upper limit for survival. At 30 C (86 F), t he r e wa s es ntially no survival at' any salinity tested. Most Mytilus pediveliger larvae settle to the bottom from mid-June through mid-July in Connecticut when' corresponding water temperatures ranged between 59.0 and 69.8 F. G::nzalez (1973) found juvenile mussels' were intolerant of sustained temperatures above 27'C (80.60F) . Such a temperature coincides quite closely to the water tempera ture G.4-90
_ _ _ ___ __ ._= _ . . _ _ _. I NEP 1&2 which identifies the boundary of their zoogeographical range. Hutchins (1947) found the southern limit of distribution' corresponds with a monthly maximum temperature of 80 F. Read and Ouunings (1967) explain the restrictions over this species natura'l range i by an upper limiting temperature of 80 6 0F. The same autho rs , howeve r, s ta te ' that according to their experimental evidence, some individuals can survive temperatures ' I as high as 85 F l Henderson (1929) recorded the upper tolerance temperature level of Mytilus to be 105.4 F. The .24-hour median tolerance was conservatively estimated at 84.20 F. Pearce (1969) t claims a behavioral perturbation rendoring Mytilus more susceptible to predation at temperatures approximating 75.20F. Conzalez (1973) through field observations and laboratory studies reported extensive E edulis mortality immediately adjacent to a a power plant discharge. He noticed that feeding ceased at .770F, and mortality was {- reported dien the water temperatures increased above 80.60F. Widdows (1973) found that I the heart beat of adult mussels became erratic, and the rate of water filtration declined' i l at 25 C- (77 F) or above. Based on observations made by the various investigators, adult Mytilids appear to be able to tolerate temperatures from 80 F to slightly above 100 0F
~
l for short periods of time (Figure G.4.2-52). Gonzales (19 73) points out, however, that - sustained water temperature approximating the lower end of this higher-temperature-a limitation range (i.e., 80 F) does cause mortality. Such .an observation is confirmed by Hutchins (1947) and Read and Cummings (1967) who in'7: ate that the natural range i { of this species is definitely influenced by naturally occurring water temperatures of 0 80 F or above. The thermal discharge of NEF 1 and 2 is not expected to cause appreciable harm to the adult population of Mytilus for two reasons: a. The expected peak plume temperature of 75-760F are within their tolerance limit, and 4 b. Within the proposed discharge area there is a limited amount of substrate (i.e., i G.4-91 I
~ . . . , , , . , . . . _ - . . _ . . _ _ _ . _ , . . . . . . _ - - - _ , . _ _ , _ . , , . . _ _ . . . _ _ _ . - - . _ , . . . _ . _ _ _ , . , _ - _
NEP 1&2 rocks) where blue mussels can attach; consequently, any interaction between the 4 thermal plume and any sublittoral community of M edulis is expected to be small. Dua to the somewhat temperature sensitive nature of the latvae, the planktonic stage of this species may be af fected to a limited degree. The overall impac t is expected to be negligible, however, due to the small area of the mixind zone relative to the cres of Block Island Sound, the species prolific nature, and the short residence time En organism would experience in the mixing zone. The thermal tolerance information available for Mytilus edulis is presented in Figure G.4.2-52. In-Plant Ef fects. Blue mussel larvae occurred for 314 days during both the 1974 and 1975 period and the 1975 through 1976 period. If NEP 1 and 2 had' operated at full ( 11 ccpacity during the period of occurrence, 6 393 x 10 ll and 2.799 x 10 mussel larvae
~ '
would have been'entra'ined during 1974-1975 and 1975-1976, respectively. Parchon (1968) indicated that mortality over 99 9% was normally compensated for by bivalves in general. Applying this mortality assumption, the above larval entrainment actimates would be equivalent to 6. 393 x 108 and 2.799 x 108 adult mussels for (1974-75 end 1975-76 respectively). Quarterly benthic sampling -in Block Island Sound f rom May 1974 through March 1976 1:dicates that sets of adult blue mussels do not become successfully established in thin area. The entrainment of blue mussel larvae is, therefore, not expected to have
' d measurable . impact on local mussel populations s'ince these entiained larvae do not ' cppear to .normally contribute to a -local sustained adult population. However, mussel Icrvae passing through this area may contribute to adult populations far removed f rom the vicinity of NEP 1 and 2. The potential impact of mussel larvae entrainment on such G.4-92 Y e =
NEP 1&2 ' populations can be evaluated by reviewing the entrainment impact on mussel populations at another. nearby coastal nuclear power facility (i.e., Pilgrim Station, Cape Cod Bay) . s Stone and Webster (197';) estimated that 2 31 x 1012 mussel larvae would be entrained through Pilgrim Station Units 1 and 2. Applying the same mortality assumption given ) above, they determined that the mussel larvae entrained at Pilgrim Station might have produced 2 31 x 109 adults. Based on densities of adult museels ,in the vicinity of Pilgrim' Station, they estimated that the loss of 2.31 x 109 adults would be equivalent to 121 acres that could theoretically be devoid of mussels. This estimate was considered conservative since no ' detectable change in mussel density in the vicinity of Pilgrim Station has occurred as a result of Unit 1 operation even though theoretically one would predic t that 32 acres should be devoid of mussels as a result of Unit 1 operation. Based on their analyses, Stone and Webster (1975) concluded that the Pilgrim Station impact on the adult mussel population would be negligible. jk , Since the mussel entrainment estimates for Pilgrim Stations Units 1.and 2 a re ) approximately 3.6 to 8.2 times greater than those predicted for NEP 1 and 2, and since mussel' larval entrainment losses of this magnitude have been previously shown to have negligible . impact on adult mussel popula tions , it is concluded that mussel larval entrainment at NEP 1 and 2 should likewise result in no appreciable harm to the adult mussel populations. Total Impacts. The mussel is a thermally tolerant species which will not be subject to entrapment. Large numbers of mussel larvae will be entrained . through the cooling water systen of NEP 1 and 2. This number is approximately the same as the numbArs Wiich are taken at Pilgrim Unit 1, a. plant which has not ef fected the local mussel population. Because of this and the low survivorship rates of the la rva e , plus the inab ility o f adults to survive in large numbers in the local area, it is believed that there will
- be no appreciable harm to this species.
G.4-93 y--r---+r 9 -~- , w- ww-wry y-w,w ,---gr-4 y- - - - -
NEP 1&2 (
'4.2.13 Ilard Clam (Mercenaria mercenaria) 4.2 13.1 Life History. The hard clam - also referred to as the " littleneck", the
" cherrystone" and 'the " quahog", depending upon its size - is a widely distributed bivalve rdollusk, its range extending from the Gulf of St. Lawrence to the Caribbean (Pratt and ,
~
Carpb ell, 1956) . Its inability to reproduce at temperatures below 20 C limits its distribution north of Cape Cod to coves and estuarine areas where localized warming may permit spawning. Because of its high degree of tolerance to a wide range in temperature and salinity, vrriations in substrate, and levels of pollution, the hard clam may be the most abundant snimal of its size in estuarine areas such as Narragansett Bay (Pratt and Campb ell, 1956). (
.1h2 hard clam spends its post-larval existance buried beneath the bottom sediment, moving e
only short distances from its. origi'nal point of settlemen t. In Narragansett Bay, Stringer (1959) found it to be most abundant in sediments composed cf mud , sand and shall. Since it is a filter feeder, extending its short siphon upwards to the water-erdirent interface and pumping its food - in the form of phytaplankton and particles of detritus - from the surrounding waters, its rate of growth is generally faster in rolatively firm sedinent where water currents typically are greater than over a sof t rud bottom. Sexto in the hard clam are separate and fertilization of the egg is external. Spawning , usually occurs when. water temperatures reach 230C (73-74 F) or more in-early summer; temp 2rature appears to act as the major stimulant to the release of eggs, and spe rm. i Sineg the presence of sperm of ten stimulates the release of eggs, spawning may al.w t G.4-94
NEP 1&2. be in response to a chemical stimulus contained within the sperm (Nelson and Haskin,1949). The fertilized egg is slightly negative buoyant. However, cleavage and embryological development proceed rapidly and by the end of 24 hours the embryo has developed into a shelled, f ree-swimming veliger larva. During the next 7-14 days, depending upon tesaperature the larvae equipped with a ciliated velum has limited mobility but presumably is at the mercy of wa ter currents, with little control over its distribution. 1 At the time of metamorphosis, the larva develops a muscular " foot". The velum disintegrates, and the larva settles to the bottom where now equipped with a byssal i gland it ' alternatively attaches itself to sand grains then crawls by means of its foot in search of a suitable substrate for burying. This exploratory period may continue for days or weeks. Ultimately the little clam burrows into the sediment by the use i of its byssal gland and if the area is favorable remains there for the remainder of its life. The growth rate of the hard clam is dependent upon and directly related to temperature as well as to salinity, current, and availability of food. In the wa ters of southern New England, it generally requires a period of two to three years for a hard clam to attain a length of five cm (2 inches); the rate of growth is inversely proportional to the size of the clam. Turner (1953) found that salinity in the range of 23-28 ppt and temperature of approximately 23 0C were optimum for growth. Hard clams may become sexually mature by their second year. Experiments by Davis (1960) indicated that the percentage of fertilized clam eggs capable of developing nonnally declined at slit concentrations of 0 75 g/1; no eggs developed normally at concentrations of 3 0-4.0 g/1. Sitt concentrations above 1.0 g/l retarded the development of clam larvae. A salinity of 27 ppt was optimum for development of eggs and la rvae ; salinitie s of 17. 5 ppt or below resulted in reduced survival. l G.4-95
NEP 1&2 I The hard clam is of major economic importance in southern New England and along the ciddle Atlantic coast where it may be found from the low water mark seaward to depths of 50 feet (01sen and Stevenson,1975). It is the basis of a valuable fishery in Rhode Island. Commercial landings in Rhode Island during the period 1971-1973 averaged 960 thousand pounds of meat, with an average annual value of 925 thousand dollars. Ninigret P0nd supports a modest commercial and recreational clam fishery. 4.2.13.2 Impacts of Construction. No adult quahogs were found in Block. Island Sound - 1 during Applicant's ba'seline studies, and larvae were found in very limited numbers. Therefore, no appreciable harm to the quahog population is anticipated as a result of construction. 4.2.13.3 Impacts of Plant Operation k Entrapment. The hard clam will not be subject to entrapment. Within the Discharge Plume. The hard clam is both a euryhaline and eurythermal species which is widely distributed f rom the Gulf of St. 1.awrence to the Caribbean. Because of its high degree of tolerance to a wide range of temperature, salinity, variatians in substrate, and levels of pollution, the hard clam may be the most abundant animal of its size in estuarine water such as Narragansctt Bay (Pratt and Campbell ~,1956) . At the proposed' site, this bivalve is only found in Ninigret Pond where it provides a modest commercial and. recreational fishery. As a result of its thermal tolerance end location relative to the thermal discharge, no thermal impact to the adult is enticipated. Davis and Calabrese (1964) reported the ef fects of temperature. and salinity on the growth of eggs and larvae of M. mercenaria. At 27.5 ppt salinity (the highested tested and closest to the salinities observed in Ninigret Pond and Block Island Sound) eggs survived G.4-96
NEP 1&2
~
temperatures between l7.5 and 30.00C (63.5 and 360F) whereas, the mean length for 12 day old larvae uns greatest at 300C (860F). In Ninigret Pond, significant concentrations of Mercenaria larvae were observed when the surface temperature was 80.6 F, the highest temperature observed. It is, therefore, concluded that the peak temperature of 75-76 F expected in the thermal plume will not adversely a f f ect Mercenaria larvae. In-Plan t Ef f ec t s . During Applicant's baseline studies, hard clam larvae were collected in relatively low numbers in Block Island Sound. A direct comparison of their density' in the Sound with densities elsewhere is more difficult than in the case of the oyster as a result of the problems associated with distinguishing the larvae of this species. The larval hard clams were not identified in the 1974 collections. Du r ing 19 7 5, a conservative maximum density of 1452/m3 was observed on August 19 The est ima te is conservative because it also includes Modiolus and Mytilus as well as Mercenaria: most of the larvae were probably m tilus. I carricker (1959) reported a density of 10,000 hard clam la.rva e / 3m in Home Pond on Gardner's Island, New York and landers (1954) reported densities of 7500/m 3 . In Ninigret Pond, Applicant observed densities of Mercenaria (not including Mytilus and Modiolus
) in excess of 16,000/m 3.
Because of the comparatively low density of larvae in Block Island Sound, it is unlikely that this species will suf fer any. appreciable ha'rm as a result of the operation of NEP 1 and 2's cooling wa ter system. Total Impacts. The hard clam is a thermally tolerant species which will not be subject to entrapment and whose larvae exist in Block Island Sound in low numbers. No appreciable harm to this species is expected as a result of the operation of NEP 1 and 2's cooling wa ter system. 4.2.14 Long-finned Squid (Loligo pealet) G.4-97
NEP l&2 4.2.14.1 Life History.' The long-finned squid, also known as the winter squid, bone . squid or common squid, is commonly found f rom Cape Cod to Cape Hatteras (Olsen and St svenso n, 1975) . According to Summers '(1969), squid may. bg found on the continental - e chalf at depths of 28-366 m (92-1200 f t), with major concentrations at 110-183 m (360-600 ft). In Block Island Sound, squid have moved into the area of Charlestown Beach in significant numbers by May and remain into December. During this time, they may comprise a significant percentage of the catch by local trawlers fishing out of Point Judith (Table G.2.3-2). Otter trawl sampling at two stations of f Charlestown Beach d'uring 1975 indicated that ' squid were significantly more abundant at a depth of 80 f t thtn at depths of 30-40 f t (Table G.2.3-3). Tha squid moves inshore each spring to spawn in shallow wa te r , i .e . , from the sho re
~
to a depth of 90 m (295 ft) (Ra thj en, 1973 ) . The eggs are contained in a series of gtlatinous strings containing 150-200 embryos each (McMahon and Summers,1971). Time ( bstween deposition and hatching varies indirectly with. temperature but, ranges roughly bstween two to four weeks during late spring and early summer in -southern New England. Summers (1971) reported that eggs appear to approach 100% hatch in nature. In Block Island Sound during 1977, newly hatched juvenile squid were first observed on June 28, 1977. Maximum abundance of juveniles was observed from July 5 through July 14, 1977 with secondary peaks in mid-August and mid-September (Raytheon,1978). The temporal cbundance of squid juveniles is presented in Figure G.4.2-53; the spatial distribution within the study area is presented in Figures G.4.2-54. Th2 squid grows rapidly, many becoming sexually mature af ter one year; the maj ority
~
dio before completion of their second year. The adult squid averages 160-180 mm in icngth (Summers, 1971). 1ha squid is an active predator, feeding upon small crustaceans as a juvenile and later G.4-98
24EP 162 upon small ' fish (Rathjen,1973). It in turn is fed upon by striped bass, bluefish and other swif t-moving predators. 9
- 4.2.14.2 Impacts of Construction. Squid have great mobility and can easily avoid the suspended sediments and turbidity associated with construction activity. Additionally, they are more abundant of fshore than near the construc tion area (Table G. 2. 3--3) . Ef fects on the eggs and juveniles are not. expected to be significant because of the small area involved and the short incubation time. Under these circumstances, no appreciable harm
~
to squid populations is expected as a result of construction activities. 4.2.14.3 Impacts of Plan t Operation Entrapment. Squid, since they are pelagic and occur near the location of the proposed intake (Table G.2.3-3), are potentially vulnerable to entrapment. However, the potential for significant entrapment of Lolino pealei through the proposed velocity cap intake
~
at NEP 1&2 appears to be remote based 'upon the experience noted at electric generating stations in California and in Florida which are currently using velocity cap intakes (CZC, 1979). This assessment is based upon the following observations: (1) the long-finned squid does occur, although not in abundance, in Flo r id a , but it has not been impinged at the St. Lucie plant; (2) Lolino opalescens, a behaviorally similar congener of the long-finned squid is commonly abundant near all of the velocity cap intekes in California, yet California Fish and Game records show tha t it is rarely entrapped. It was found to be entrapped in only 9 out of 155 sampling periods between September 1975 and April 1978. The total weight of entrapped squid during this peribd was less than forty pounds; and, (3) the long-finned squid has an exceptional swimming ability. According to Barnes (1969), squid attain the greatest swimming velocity of .any of' the aqua tic invertebrates.- Cole and Gilbert (1970) reported that squid have an average swim speed of 6.5 f ps. Fu r the rmo re , Loligo is known to feed on young mackerel by swimming backwards into a school and seizing its prey. Since mackerel less than one G.4-99
NEP 1&2 year old can sustain a speed of s'ix knots (fps) (Bigelow and Schroeder, 1953), it is i assumed that squid are able to attain a similar velocity. It is, therefore, expected that the squid will' be able to avoid or escape from the intake currents and, hence, no appreciable harm on the population is predicted. Within the Discharge Plume. McMahon and Summers (1971) reported that the long-finned equid deposi'ts its eggs at temperatures between 10 and 23 C (50 to 73.4 F) . These same authors found the rate of development of squid embryos appeared to be directly related to sea water temperature. In their experiment h pealei embryos were readily maintained in the laboratory between 12.0 and 23 C (53 6-73 40F ). Temporally, Raytheon (1978) reports squid egg clusters observed in Block Island Sound from May to October. Spatially a greater abundance of egg clusters were found at the inshore station than at the two offshore stations. Such findings . would indicate the potential exists for some interface between the discharge plume and attache'd squid egg ( a clusters. Inaanuch as the induced bottom temperature isotherms would approximate natural egg laying temperatures, described in the literature (i.e., 50-73 F), no appreciable thermal impact is expected.
&an development time for spawning to hatching is related to water temperature.- McMahon and Summers, (1971) report squid hatching in approximately 27' days at 12.0-18.0 C (54-640F ),19 days at 15. 5-21. 3oC (60-710F) and 11 days at 21.5-2 3.0 C (71-740F) . Raytheon (1978) also found that the majority of squid juveniles were collected only when water temperatures ranged between ISOC to 210C (59-70 F) . Even though juvenile squid were cellected from June to October, the majority of , juveniles were.ob. served in July when 0
mean surface and bottom temperature reached 18 9 C (66 F) and 15 7 C (61 F) respectively. 1h2 five month interim (i.e., June-October) when juvenile squid are found in Block Island Sound coincides with an induced surf ace temperature range of 63-750F. When such results G. 4-100 1
. J
EEP 1&2 are compared with the juvenile development temperature range presented in McMahon and Summers (1971) it seems rather improbable that the Applicant's thermal discharge would af fect this early life history stage. Summers (1969) reported a pronounced reduction in squid bottom catches at temperatures less than 80C (46.40F), while Serchuk and Rathjen (1974) found highest concentrations of squid in water of 10-12 C (50-53.6 F) during the spring and 10-14 C (50-57.20F) during the fall. Adult squid were observed in the vicinity of Applicant's proposed discharge site during the months of May-November, coincident with a surface temperature range of 46-70 F. Similar to the findings of Serchuk and Rathjen (1974), peak abundance occurred in October, corresponding to a temperature range of 54 to 57 F. Should similar temporal tendencies occur during plant operation, adult squid would experience an induced surface temperature from a low of 52 F to a high of 76 F. Even though there is the possibility that squid may contact the surface discharge during their seasonal insho re ( activities, thermal impact is expected to be negligible since the geographical range of this species implies existence in waters equal to or warmer than those anticipated as a . result of plant operation (NOAA, 1973). In-Plant Effects. Squid eggs are laid in gelatinous strings on the bottom and, therefore, are not subj ec t to entrainment. No intermediate planktonic larval f o rm, as in the gastropods or pelecypods, is produced (Barnes 1969) and juvenile squid hatch directly from the egg. During 19 77, j uvenile squid occur red at the location of the proposed in tak'e fo r approximately 133 days. Based on calculated average densities and assuming 1007. plant load duri.ng their period of occurrence, 1.983 x 106 squid juveniles (all ages) would have been entrained in 1977. To determine the number of one year old squid that would have resulted from this G. 4-101
NEP 1&2 F entrainment, this entrainment estimate was converted to the equivalent number of squid ( juvsniles at hatching by applying the procedures discussed below. x Lengttefrequency data obtained on squid juveniles collected during the 1917 survey wer,e usad to develop a method for aging juveniles. From each weekly. collection of squid, th3 largest juvenile was selected and its age was estimated." During the time period of 28 June through 14 July 1977, the hatching date for this oldest individual was assumed to be one week older than the first occurrence in the samples. Af ter 14 July 1977, tha largest squid in the sample was assumed to have hatched at the mid-point of the major hatching period (5 July through' 21 July 1977). A linear regression line was then fitted to the data utilizing the standard least squares technique. Inspection of the regression revealed that the equa tion overestimated the ' age of recently ha tched juvsniles, but that the confidence limits on the value of the intercept included the known length at. hatch point (2 mm mantle length; Arnold,1965). The regression line { was, therefore,' rotated around the grand mean of age and length and forced 'through the point age = 0, mantle length = 2mm. The resulting equation for estimating the age of equid juveniles is: Age = -3.28 + 1.64 (Length) whsre: Age is in days and Length is mantle length in millimeters
- Tho .above equation was then applied -to the squid juvenile data, and age-f requency distributions by survey were developed. Age-specific totals of squid juveniles for all surveys were calculated and regressed to the general f ormt N - No e-Zt fo r time (
intsrvals from hatching to each age represented. The regression coef ficients, Z, f rom G . 4-102
NEP 1&2 these analyses provided estimates of total' instantaneous mortality rates. Severri of the estimated total mortality rates for various age squid juveniles are presented .in the following table: M Survivorship Z / Day , Juveniles Hatch - 12 days 0.0044 0 452 Hatch - 79 days 0 0029 0.072 79-365 days 0.0807 0.0088 Ilatch .- 12 months 0 0002 0.0229 - Adults 12-24 mons.hs 0.19 0.0045 The age-specific total mortality rates were then used to determine the equivalent number o f squid j uveniles a t .ha tching for each s'urvey by applying the e'qua tion: Ng = Et-- ( e -zt where: No = number of squid j uveniles a t ha tching N = number of squid juveniles a t time t t Z = to tal instan taneous mo rtality rate , and t = time in days. These estimated numbers of equivalent equid juveniles at hatching (No ) for each survey were then divided by the actual numbers of juveniles collected to derive a correction factor for transforming the mixed-age squid juvenile densities to the estimated densities of juveniles at hatching. These densities' of squid juveniles at hatching were then used to evaluate the impact of entrainment. G.4-103
NEP 1&2 B3 sed on the projected average densities of juveniles at hatching, and assuming 100% pitnt load, an equivalent of 3.798 x 107 squid juveniles at hatching would have been entrained in' 1977. From the data of Vovk (1974) and Raytheon (1978), Applicant developeh l the following length-fecundity relationship for squid: -
- 1 F = -4147.80 + 636.56 ML wehre: F = fecundity, aml
; ML = mantle length in centimeters a
Suseners (1971) reported on the age, growth, and age class structure of a squid population in the inshore region of Menemsha Bight in southern Vineyard Sound. Summers suggested that approximately one-fourth of the egg deposition around June was carried out by two year old females and that two year olds probably account for less than one-quarter of tha total breeding population and contribute no more than one-third of the brood. He . ( further stated that the squid stock is basically annual but that males may live to 36 months (although more frequently only 24 months) while females have a maximum lonevity of 19 months. During late May (just prior to spawning), Summers reported that 16% of tha adults (Applicant assumed 16% of the females) were age 2. From this information
. plus previously presented fecundity relationships, a Leslie population projection matrix was constructed ditch desetwd a stable population (the eigen value or finite population growth rate was 1.00). Li this model, the survival rate from egg to age 1 was determined ~
by a numerical method presented by Vaughan and Saila (1976). Population values used iri the Leslie matriy are presented in the following life table Fecundity
.A_ge Per ' Adult Survivorship Relative Frequency O. 0 2.3486 x 10-4 1,000,000 1 3019 0 19 235 2 6520 0 45 G . 4-104
NEP 1&2 From this table, it can be seen that less than 0.03% of squid that hatch woul.1 be expected to survive to the following year. Assuming a stable population, Summers (1971) estimated that only 0.05% of the hatched juveniles survive to the followin'g year. ' Based on the estimates of So by Summers (1971) and Applicant, the projected entrainment of squid juveniles at hatching would result in the loss of 18,991 or 8,921 one year old squid, respectively. The weight of these squid can be estimated by length-weight relationships reported by Tibbetts (1975): Males: W = 0.005592L1.86345 Females: W.= 0.000931L2.26429 where: 4 = weight in grams, and ( L = length in millimeters. Summers (1971) found that the average size of one year male and female squid was 180 mm and 160 mm, respectively. Assuming a 1:1 sex rat' io, and based on Summers (1971) estimate of So the estimated number of one year old squid not recruited to the population due to entrainment would weight approximately 3771 pounds or 1.7 metric to ns . Based on Applicant's estimate of So, the projected loss of one year old squid would weigh approximately 1771 pounds or 0.8 metric tons. In their preliminary fishery management plan for squid fisheries of the Northwest Atlantic, NOAA (1977b) assumed (in the absence of evidence to' the contrary) that the
' fishing for long-fianed squ'id' of f the northeastern USA exploits a single stock distributed from Cape Hatteras to the northern edge of Georges Bank. During 1968 to 1975, minimum st'ock size esti ates for the af fected ' region (subarea 5 and 6 ) r ang'ed G. 4-105
NEP 1&2 l from 221,100 tons to 97,303 tons (Sissenwine, 1976). The projected loss of one year old squid due to entrainment at NEP 1 and 2 is equivalent to less than 0 008% of the cinimum stock size in this area. Since 1969, squid landings in Rhode Island have ranged from a low of 319 metric tons in 197.1 to a high of 1166 metric tons in 1976. In 1976, inshore (0-3 miles) landings of cquid in Rhode Island totalled 428 metric tons (Raytheon,1978). The projected loss
'of one year old squid due to entrainment is equal to less than 0.5% of recent Rhode Ialend squid landings.
Bectuse of the low magnitude of entrainment losses when compared to the squid stock cize and Rhode Island landings, Applicant believes that squid populations will not suf fer appreciable harm as a result of juvenile entrainment. Tecn1 Impacts. The squid is a species which will probably be entrapped and possibly (. sntrained in small numbers. There is no reason, based on experiences at other New England power plants, to suspect anything to the contrary. Squid eggs are demersal adhesive and are, therefore, not subject to entrainment. The imp ct of entraining squid juveniles was shown to be less than 0 5% of recent Rhode Isicnd landings, and less than 0.008 % of the minimum stock size estimate of the squid p;pulation in the northwest Atlantic. Vary little information is available on the squids' temperature tolerance. However, it is known to live in waters equal to or warmer than will be found in the thermal plume. It is, theref. ore, expected' that there will be no appreciable harm to this species as a rsault of the operation of NEP 1 and 2's coollag water system. G.4-106
NEP 1&2 4.2 15 Sand Shrimp (Crangon septemspinosa) 4.2.15.1. Li fe History. The sand shrimp (Crangon septemspinosa (Say), fo rmerly Crago - septemspinosus) is an epibenthic decapod species with no direct commerc ial or recreational value. It is, however, of considerable importance as a source of food for commercial and sport fishes and other organisms higher in the food chain. Price _ (1962.. states th'at C. septemspinosa "is prominent in die ts of numerous carnivores includiig weakfish, skates and rays." In a study on the benthic invertebrates of Block
' Island round and their relationship to fishes, Smith (1950) found C. septemspinosa in-stomache of skate, sculpin, flounder, sea robin, windowpane, eelpout, whiting and other fish. Crangon ranked fourth and averaged 7.6% of total consumption of invertebrates by fishes. ' Sand shrimp is found inhabiting various bottom types from Baf fin Bay to Eastern Florida _ and from the nearshore zone to depths of 450 meters (Haefner,1972; Price, 1962; Whiteley, 1948).
I Sand shrimp is a permanent resident in Block Island Sound. Juvenile C.; septemspinosa I were daninant in fall and adults during late winter early spring at station EB-C in Block Island Sound (Raytheon, 1979). Smith (1950) also collected C. septemspinosa throughout the year in Block Island Sound with most being collected during tha ' winter months . There is evidence of seasonal movements onshore and of fshore (Raytheon 1979). ; However, Wilcox and Jef fries (1973) were unable - to collect many individuals from the Pe t taquamscut t River in Rhode Island during the winter and spring, and Haefn'er (1972) reported that C. septemspinosa from Lamoine, thine appeared in the shallow tidal flat and beach areas in late April or early May and that the larger shrimp began to disappear as early as November with most adults gone by December.
~
Squires (1965) reported an onshore-of fshore migration in the Gulf of' St. Lawrence. Migrat' ion of fshore in the warm months instead of the' cold months was indicated by Williams (1965) for North Carolina 1:.,septemspinosa. In constrast to the above, Price (1962) did not observe seasonal G. 4-107
~
NEP 1&2 ( eig rations in Delawa re Bay - near the mid-po in t of the sand shrimp's range.
~
While this species is generally epibenthic, it does burrow into the bottom (Price,196d)' , and is occasionally found in, the plankton (Hopkins, 1958), particularly after storms
- (Bigelow and Sears, 1939). crangon septemspinosa is apparently omniverous although it has a preference for animal material. Wilcox and Jef fries (1974) reported .that 85%
of the stomach contents of their specimens was organic debris and that the remaining 15% consisted of sand, crustacean parts, copepods, plant material and polychaetes. Ovigerous (egg carrying) females were present in trawls collected at EB-C f rom January through June in Block Island Sound (Raytheon,1979). At Lamoine, Maine ovigerous . females were present from May through September (peak numbers in July and August) (Haefner, 1972) and in all months except December (primarily March to October) in Delaware Bay (Price, 19f,2). Larvae are planktonic until they attain a length of approximately '4 [ mm (Tesmer and Broad,1964). i Larval stages of L septemspinosa were found in the water column in Block Island Sound ystr-round with the greatest concentrations occurring f rom April to November (Raytheon, 1979) (Figure G.4.2-55). The distribution and average density of sand shrimp larvae found during 1978-1979 is shown in Figure G. 4 2-56 and G.4. 2-5 7. ) . Hillman (1964) rzported them in Narragansett Bay from May to October.
.Tha largest sand shrimp Price (1962) captured in the Delaware Bay was 70 mm (three and ens half years old with 7,500 eggs). The largest individual collected by Wilcox and Jpfferies (1973) was approximately 60 mm long.
4.2.15.2 Impacts of Construction. Because of their mobility and the fact that they cra able to live within the bottom, sedimentation is not expected to affect sand shrimp prcsent in the vicinity of construction activities. Some larvae will undoubtedly be lost; however, in view of the small area and short time period involved, no appreciable G.4-108
NEP 1&2 harm to the local population is expected. 4.2.15.3 Impacts of Plant Operation Entrapment The entrapment potential of the sand shrimp is dif ficult to assess because of a lack of data at other generating plants having velocity cap intakes. It ,is likely that the small size of these animals enable them to pass completely through the cooling water system and thus fail to be recorded in impingement data. Little information is available about their swimming capabilities and those behavioral characteristics which would enable one to determine their ability to avoid entrapment. In California, a similar species, Crago nig romacula tus , was among the most common arthropods collected in the vicinity of the Ormond Beach Generating Station (MBCI,1972), yet it is not recorded as having been impinged. ( - Among those characteristics of adult Crangon which argue against its being entraped. in significant numbers by NEP 162 are: ,( J its preference for unobstructed sandy bottcas; (2) its tendency to burrow beneath the sand; and, (3) its benthic habits and nominal absence from the water column. It may become more available for entrapment during periods when storms agita te the bottom substratum and cause the shrimp to become plankt o nic . It is further possible that the shrimp may be entrapped in large numbers during seasonal migrations if they do not occur among the populations in Rhode Island Sound. Such migrations are known to occur among sand shrimp in Maine but do not occur in the Delaware Bay region. 1 Within the Discharge Plume. The sand shrimp is eurythermal and has been collected within
- a. temperature range of near freezing (O C) to .the mid. to upper 20 C 78-85 F) (Price, 1962; Haefner, 1969, 1976; Vernberg and Veruberg 1970). The available temperature r
I tolerance and thermal characteristics information is presented in Figure G.4.2-58. G.4-109
NEP. 1&2 Hazfner (1972), in his discussion on the biology of the sand shrimp cites Tiews (1969), I-a f ter Meixner, 1966, 1967) who reported that under optimum feeding conditions Crangon crsngon eggs hatch af ter .three weeks incubation at 180C (650F); af ter 4 weeks at 140C (580F) and af ter 10 weeks at 6-100C (43-500F) . In a cursory study conducted by Price . (1961), hatching of L septeaspinosa eggs was observed af ter 6-7 days at an incubation tepperature of ' 210C (700F) . Inasmuch as the sand shrimp is strongly bottom oriented, tha egg carrying female is not expected to be greatly influenced by the NEP 1&2's discharge plume since she can move from the area should it prove un tenable. Planktonic sand shrimp larvae have been found year-round in Block. Island Sound (Raytheon, 1979). Such a temporal occurrence corresponds to an expected induced sur f ace water 0 Sandifer (1973) in examining the temperature range of 7.2 - 23 9 C .(45 -75 F) distribution and abundance of decapod crustacean larvae in York estuary in adjacent lower Qiemake Bay, captured sand shrimp larvae between 1.5 and 26.2 C (340 and 79 F) . ( Larvae were most abundant, however, between the temperatures oY U O -20 CC (59 -68 F) . At stations EB-B and EB-C in Block' Island Sound the overall abundance of sand shrimp larvae was higher in near bottom waters than in surface waters (Figures G.4.2-56 and G.4.2-57) with evidence of diel vertical migration (Raytheon, 1979). During the day larvae densities were greater in near bottom waters, wF .reas at night larvel densities cppeared to increase near the surface. In contrast, Sandifer (1973) pointed out that oend shrimp larvae were not especially abundant near the bottom in York estuary. Of tha larvae he did collect, 59% occurred in the near-surf ace samples. The natural temperature range for larval development (Sandifer,1975) encompasses those _ induced curface temperatures expected from the operation of NEP 1 and 2. . Inasmuch as most tpecies characteristic of north temperate waters are capable of existing in temperatures et least a few degrees higher than their natural range for short periods of time. it to believed that there will be no' appreciable harm to those larval stages entrained in the plume. G.4-110
NEP 1&2 i a Most of the published thermal tolerance studies conducted on the adult life history stage, focuses on temperatures encountered in their natural environment. Haefner (1976) in studying sand shrimp abundance in the York River, Chesapeake Bay estuary, captured 1~ sand shrimp in the temperature range of 0. 5-24.10C (33 -760F) . Maximum concentrations were encountered however, in the winter between 5 and 11 C (41 -52 F). He observed that sand shrimp concentration was reduced once the water temperature reached ISOC (59 F) . In an earlier paper, Haefner (1969), described the temperature and salinity tolerance of the sand shrimp in the Penobscot River estuary. He reported sand shrimp were never observed' at any embayment where water temperatures were in excess of 22 C (720F) regardless of the salinity. In another study, Haefner (1970) studied the ef fects of low dissolved oxygen concentrations on the temperature / salinity tolerance of adult i sand shrimp. Greatest mortality was observed around 23 C (740F) . Vernberg and Vernberg (1970) noted that in general, animals with northern .af finities (such as the sand shrimp) did not survive high water temperatures as well as those with more southerly displaced limits. Sand shrimp captured in February, were . observed to die most rapidly at 25 C (77 F). Heldrim et al. (1.974) reported that L septemspinosa captured in the Delaware River estuary had preference temperatures of 79 and 550F (26 and '13 C) when acclimated at respective temperature of 43 and 40 F (6 and 4 C) . i Adult sand shrimp were found in Block Island Sound year round, corresponding to. induced surface temperatures of 7.2-23.9 C (45-750 F). Based on the observations made by the various investigators, adult sand shrimp appear to be able to tolerate any temperatures Wich may occur in the thermal plume. Because this species is mobile and eurythermal, interaction with the thermal discharge plume is not expected to harm the sand shrimp. In Plant Effects.- In 1978-1979 sand shrimp larvae were observed in the water column G.4-111
- ,..e--.---- -_ __ --_._---p. . . . - _ _ v_,_--..,-:---- -
,_.. __ ~ - . . - . . _ . - . . ~ _
- , ,_____-_7
NEP 1&2 thrcughout the ' year with significant abundance levels occurring f rom March through - November (Raytheon, 1979). In Narragansett Bay Hillman (1964) found its frequency o,f occurrence l' onger than any other decapod larvae, occurring f rom May through October. Based on calculated average densities and assuming 100% plant load throughout the year, 2 982 x 109 sand shrimp larvae would have been entrained from May 1978 to May 1979. To determine the number of adult Crangon that would have been lost through entrainment, cl1 larval stages were converted to equivalent stage I. During 1978-1979 the average percentage of all larval stages was: Stage 1 - 32%, Stage II - 13%, Stage III - 8%, Stage IV - 8%, Stage V - 11%, Stage VI - 11%, Stage VII - 12%, and post-larvae - 5%. Since these ratios were not useful to generate a population survival curve, mortality was estimated based on data supplied by Temer and Broad (1964) for sand shrimp larvae cultured in laboratory at 18 -20 C on an Artemia diet. An age-cpscific mortality rate for larval stages was calculated f rom the general' form Nt ?No e-*U for time interval's from hatcing to post larval stage. This yielded a mortality of Z=0. 096 7/ day . Hillman (1964) estimated a mortality of 22% from one stage to the next for natural populations of Crangon larvae. However, this rate was not used because ha cnumerated only five larval stages where in reality there are 7-9 larvae stages of E septeaspinosa (Tesmer and Broad 1964). Consequently, the previous mortality rate was used since it provided a conservative estimate. Th3 age-specific mortality rate of larval ,C_. septemspinosa was used to determine oquivalenti numbers of larval stages a t'ha tching by using t h e a. q u a t i o n : G.4-112
. - NEP 1&2 tr Ng . Nt ; e Zt where:
No = number of larval' sand shrimp at hatching i N t = number of larval sand shrimp at time t Z = instantaneous mortality rate (0.0967/ day)
, t = time in days j Based on an estimated average density of larval sand shrimp at hatcliing, and assuming i
100% plant load, an equivalent of 6.387 x 109 Stage. I sand shrimp would have been entrained in 1978. To determine the number of adults that would have been lost through entrainment of these larvae, the following assumption was made. If the population is in equilibrium, the , fecundity of a female will be reduced to two breeding adults in I one generation or 9 S = 2/F ? where: S = survival f rom egg to adult, and F = fecundity of a breeding pair during their life. Survival from egg to adult is a product of survivorship from egg to larvae and larvae to adult. For conservatism survivorship from egg to larvae was assumed to be 100%. Haefner (1976) provided a fecundity relationship of Y = 2 611 + 0 00 7 7 (X-15 6516 ) where t l 4 i G.4-ll3 'l
NEP 1&2 Y = number of eggs per female ( X = cubed length in mm. He found egg bearing females ranging in size from 16-70 mm. Smith (1950) ' never found. rdult ' sand shrimp greater than 30 mm. Beach seine data from Ninigret Pond f o r 197 8 showed that 76% of adult Cranaon were less than 40 mm (YAEC,1979). Using a mean length of 30 mm for ovigerous females a fecundity of 1614 eggs per female was caiculated. This provided a survivorship f rom hatching to. adult of 0124%. Bac:d on estimates generated by Applicant, the projected entrainment of larval sand thrimp at hatching would result in the loss of 7.92 x 106 adults. 1h2 weight of these adults lost due to entrainment was estimated f rom the length-weight ralctionship provided by Wilcox and Jeffries (1973). ( Log W = 0.040L + 1.0 whsre: W = weight (mg) L = Length (mm) Baced on Applicant's estimate, the projected loss of adult shrimp would weigh 1.256 x 10 6g (2763 lbs). Smith (1950) estimated the standing stocks of E septeaspinosa in Block Island at'0.239 2 g/m . Assuming an area of 400 sq mi, the estimated loss of adult shrimp represent 0.5% cf the standing stock of sand shrimp in Block Island Sound in 1949. Smith also estimated that fish consumed 5 5g of food /g of fish / year and that sand shrimp ' comprised 7.2% of the stomach contents of fish. Therefore the amount of adult C , G . 4-114
NEP 1&2 _septemspinosa lost due to larval entrainment would result in the loss of 3.0 x 10 g 6 or 6.6 x 103 lbs. of fish per year which is 0.0089% of Rhode Island , commercial landings for 1978 (74.513 x 106.lbs). l Because of the magnitude of entrainment losses when compared to projected a'dult losses ) I f of fish in the next trophic level to Rhode Island commer,cial landings, Applicant believes that sand shrimp populations will not suf fer appreciable harm as a result of larval entrainment. Total Impacts. Since sand. shrimp are found throughout the year in Block Island Sound, their' thermal tolerance.are suf ficient so tha t the thermal' discharge plume will .no t result in any appreciable harm to their populations. Because of their small size they will not be subject to entrapment in any significant quantity. A conservative estimate of the number of adult sand shrimp that would have been lost due to estimated May 1978 to May 1979 entrainment of larval sand shrimp and the resultant loss of their consumers
\
showed that the impact would be small when compared to Rhode Island commercial fishery. Consequently, Applicant believes that the operation of the heat dissipation system of NEP 1&2 will not result in appreciable ha rm to the sand shrimp popula tions. 4.2.16 American Lobster (Homarus ame r ic anus ) 4.2161 Life History. According to Saila and Pratt (1973), the lobster is the most valuable product of the northwest Atlantic fisheries, with the major fishery extending from Cape Cod to the Gulf of St. Lawrence. According to these authors approximately one-fif th of the total U.S. landings are caught inshore between Cape Cod and New Jersey. As the inshore stocks have declined due to intensive fishing, the ef fort has concentrated more and more of fshore, where lobsters may be potted at depths down to 14,500 f eet. During 1974 and 1975, a few adult lobsters were taken in the otter trawl sample.s collected off of Charlestown Beach; the largest numbers were taken during the late G.4-115
NEP 1&2 apring, summer and fall. he paucity of lobster pots set within the study area implies I that commercial fishermen do not consider that the area contains a significant lobster stock.
> ~
he inshore populat' ions are believed to undergo ouly limited seasonal migrations as a rule, moving of fshore into deeper water in late fall and returning closer to shore in the spring. According to Cooper and Uzzmann (1971), members of the of fshore populations may undertake more extensive seasonal movements inshore and of fshore; the c:an dispersal radius of tagged lobsters was 50 idm (nearly 30 nautical miles) . Saila rnd Flowers (1968) described lobsters traveling up to 218 km (120 nautical miles). Iobsters are normally secretive in behavior, seeking shelter in burrows or beneath rocks. B y are carnivorous and feed upon a variety of fish and invertebrates, including fellow
. lobsters. heir cannibalistic tendency makes availability of adequate shelter imperative and may limit population density in certain areas.
( La breeding behavior of the lobster in captivitiy has been described by Herrick (1896) and Templeman (1934). Mating- can occur only during a relative brief period immediately following molting by the female, and, according to Hughes and Matthiessen (1962), no cuccessful matings have ever been observed at the Massachusetts State Lobster Hatchery 48 hours or more af ter molting occurred. Russell and Borden (1975) have. reported that in. Rhode Island Sound there are two optimal periods for molting; these. periods are late cpring and fall. During 'the mating process, the male lobster inserts the spera into tha seminal receptacle of the female. The eggs, fertilized as they are extruded cyproximately 9-12 months later, are attached to the swimmerets of the female beneath har abdomen. hey remain in a cluster until hatching af ter an additional 9-12 month psriod. he number of eggs extruded varies directly with the size of the female and rcnges from 5,000 to 125,000 (Bar,dach et al.,1972). G.4-116
NEP 1&2 All eggs from ont female hatch within a week or two depending upon tempe r a t u r e . At 200C (680F), all the eggs of a female will hatch within 2-3 days, whereas 10-14 days are required at ISOC (590F) (llughes and Kit thiessen, 1962). llatching ot lobster larvae in New England coastal waters generally occurs when wa ter temperatures are approximately 12 to 150C (54 to 590F) (Rayt heon 19 7 7 ) . The first three larval stages are entirely planktonic and f ree swimming. By the fourth molt, the larvae resemble the adult yet continue to swim for several days before becoming bottom seeking. By the fifth stage, the lobster is primarily benthic; however, swimming has occasionally been reported (Cobb,1976). During its first growing season, the juvenile lobster molts an average of ten times, at the conclusion of which it may average 13. 5 mm (approxima te ly one-hal f inch) in carapace length. Nlting frequency declines with age, averaging three to four in number during the second year, three during the third, two during the fourth, and only one . i, or less at age five onwa rd. By the end of their fif th growing season, . lobsters in captivity averaged 82.2 mn (3. 3 inches) in carapace length. . (llughes and K2tthiessen, 1962). The legal size is 3-1/16 inches (78 mm) carapace length in Rhode Island.
'Ihe number of lobsters that have become sexually mature by the time legal size is attained appears to vary with sex and geographic location. For example, along the Maine coast Krouse (1973) reported that only a very small percentage of females become sexually mature below 90 m carapace length daile most males were sexually mature at approximately 55 mm carapace length. In Long Island Sound, Smith (1977) observed that 25-64% of the sublegal size female lobsters were sexually mature.
The temporal abutidance of lobster larvae is presented in Figure G.4.2-59; the spatial distribution within the study area is presented in Figur e s G. 4. 2-60 and G. 4. 2-61. 4.2.16.2 Impacts of Construction. Adult lobsters are present in the construction area C.4-ll7
NEP 1&2 in very low numbers; those which are present have suf ficient mo'bility to avoid or move ~ away from the construction accivity. Lobster larvae which have a relatively short pignktonic life are expected in the area of construction from Rty to August. Although it is passible that relatively high concentrations of larvae may be found, it is expected that their time of passage through the area of suspended sediments and turbidity will 1 be very short and limited to the immediate area of construction. Under these circumstances, no appreciable harm to the lobster population is expected as a result of construction activities. 4.2.16.3 Impacts of Plant Operation Entrapment. Bimonthly sampling with a commercial otter trawl near the location of the proposed intake from April 1975 through March 1976 f ailed to net a single lobster. During 1978, a study was conducted to determine the population structure and harvest ( rats of the lobster fishery in the immediate vicinity of the proposed NEP 1&2 (Marcello at al., 1979). Mean legal catch rates per pot per .setover day ranged from 0.13 to 0.23; rates similar to the lower rates for Narragansett Bay and Rhode Island Sound (Russell et al.,1978). Generally, there was no significant dif ference in the mean catch rates cf lobsters from dif ferent areas. The catch rate of sublegal unberrien female lobsters in the area of the proposed NEP 1&2 intake and discharge, however, was within the group of station means that were found to be significantly lower than average catch rates in other regions of the study area. Their abundance is apparently no greater than that cf cther inshore regions of. Rhode Island coastal waters. Tha ability of lobsters to endure various sustained swimming speeds has been reported by Hyman and Mobray (undated) . These investigators found that lobsters with a carapace
~
length of 1.4 to 3'.5 inches could endure water velocities of 1 3, 2.1, and 2 9 fps for i j tina periods of at least 60 minutes. Based on the above 'information, lobsters which l i G.4-ll8
NEP L&2 o might encounter the NEP 1 and 2 intakes should be able to escape f rom the induced intake currents and avoid entrapment. Therefore, since lobsters do not appear to occur in substantial numbers near the intake location, and since their benthic life style and swimming capability would tend to preclude entrapment, no appreciable impact on the lobster population is predicted. Within the Discharge Plume. During 1974 and 1975, Applicant observed adult lobsters in otter trawl samples most frequently during late spring, summer, and fall. Observations made from neuston net studies initiated during the early summer oi 1976 have revealed the presence of lobster larvae directly off Ninigret Pond. As described earlier in the lobster life history section, female lobsters retain the eggs by attaching them to her swimmerets. As a consequence, no thermal impact is expected for eggs since the female can move from an area should it prove untenable. ( Records maintained at the Massachusetts State Lobster Hatchery indicate that ha tching usually begins in Rty when water temperatures have reached 15 C (59 F), with most intensive hatching occurring during June and early July when water temperatures reach 200C (680F) . At 20 C, the hatching process for an individual female is generally completed within a 2-3 day period. The duration of the planktonic larval period varies indirectly with temperature. According to Perkins (1972) and Hughes et al., (1972), the respective rate of development for lobster embryos and post larval stages are strongly influenced by temperature: with a positive relationship up to temperatures of 24-25 C (77 F) . According to llughes and Matthiessen (1962), the time required for newly hatched larvae to reach stage IV varied from nine days, at an average temperature of 22.3 C (72 F), to as long as three to four weks at tanperatures averaging 17 C (62-63 F ) . Molting rarely occurs at temperatures below 10 C (50 F) but resumes at 15 C (59 F) the following year. By the fifth stage, G.4-119 t
NEP 1&2 tha juvenile lobster usually seeks the bottom and shelter, where it remains for the ( remainder of its existence. As cited by Smith (1974), an excellent review of lobster temperature ef fectb has been produced by McLeese (1956). Thermal acclimation for this species appears to.be
.tecomplished from about 58 to 73.40 F within 22 days. Upper lethal temperature levels were investigated for lobster acclimated at 41 F, 59 F and 77 0F.
With a' test salinity of 25 o/oo and 4.3 mg/l of oxygen, the upper lethal temperdtures were 71.80F, 82.8 F and 85.10F, respectively. , The lobster larval stages according to Perkins et al., (undated) are more tolerant of high' temperatures than is the adult. In thermal tests conducted on the first through fourth larval stages, these investigators claim no mortality with a short term exposure 1 of 87.8 F and .only minimal loss at six hour exposures of 80.6 F. The results of their sxp2riments are generally in agreement with the observations of McLeese (1956) and Huntsman (1924) with regard to the acclimated lobster's ability to tolerate increased ttvperature. A recent investigation covered in the environmental studies report fo r Boston Edison Company's Pilgrim Station show some lobster larvae survival (TL50) at 84.5 F for 24 hours, 850F for 2 hours, and 910F for 1 hour (Battelle Columbus Laboratory, 1972). Obviously, since lobster larvae.'are generally , associated with the surface component of the plankton, there is a very good possibility that tiiey will be found in~the thermal , plume. On the basi,s of -the literature, natural water temperatures would have negligible offect on the planktonic stage of this species. A 60F, increase in the natural surface
. watar temperatures woul'd approximate a surf ace maximum of 75-760F inside tt$e boundary of the mixing zone, such a temperature is 'well within the tolerance range ind ic a ted by both Battelle Columbus Laboratory and Perkins. .
G. 4-120
NEP 1&2 Similarly, adult the rmal tolerance studies indicate induced water tempe ratures fall with'in the tolerance capabilities of the adult. The likelihood of thermal impact upon the adult is further reduced due to its ability to move out of an area should it prove unsuitable. The thermal tolerance infonnation available on the lobster is depicted in Figure G.4.2-62. In-Plant Ef fects. During 1977, lobster larval stages 1, II, til and IV occurred at the location of the proposed intake. for approximately 57, 56, 35, and 29 days respectively. Based on calculated average densities (mean of day, night, surf ace and bottan densities) and assuming 100% 'p1' ant load during their period of occurrence, 3.820
~
x 105 stage I, 6.675 x 104 stage 11, 3.154 x 104 stage III, and 1.450 x 104 stage IV lobster larvae would have been entrained in 1977. in 1976, lobster larvae were not sampled until the hatching period was well underway ( (Marine Research, Inc. 1977). Furthermore, no stratified samples were taken nor were day-night effects fully investigated. Nevertheless, comparison of larval densities calculated for 1976 and 1977 revealed that 1976 larval densities were substantially higher than those in 1977. Because of this higher density and therefore the potential.
. for greater entrainment ef fects, Applicant ' utilized the procedures described below to estimate the 1976 entrainment of lobster larvae.
For similar periods of occurrence, the average surf ace density of lobster larvae by , stage for 1976 and 1977 were compared. From this comparison, it was determined that the 1976 average surface density of stage I, II, III and IV lobster larvae was approximately 1.33, 3 44, 5.24 and 24 times greater than the densities for 1977. . The 1977 lobster Igrval entrainment estimates by stage were multiplied by the above factors and were assumed to approximate 'the 1976 entrainment of lobster larvac. This projected
.1976 entrainment was 5.080 x 105 stage-I, 2 296 x 105 stage II, 1 653 x 105 stage II, G. 4-121 l
l b
NEP 1&2 and 3.480 x 105 stage IV. f
- hsse stage specific entrainment estimates were then converted to theentrainment$f equivalent stage I larvae by applying appropriate conversion factors determined from tha' larval survival data of Scarratt (1964), Lund and Stewart (1970), and survival coefficients derived by Applicant by simple ratio of the 1977 average Block Island Sound larval densities reported by Raytheon (1977). 'Ihese equivalent stage I entrainment conversion factors are presented in the following table:
Conversion Factor to Equivalent Stage I Entrainment Lobster Larval Entrainment Scarratt Lund & Stewart Raytheon Estimate f or S tage . (1964) (1970) (1977) I 1.0 1.0 1.0 11 6.8 1.4 2.5 III 27.4 15 4.4 IV 88.8 1.9 13 3 k The estimated 1976 entrainment of equivalent stage I larvae obtained by applying the above conversion factors ranged from 1756 x 106 for conversion factors derived from
- lund and Stewart (1970) to 3.749 x 107 for conversion factors derived f rom Scarratt (1964). The estimated 1977 entrainment of equivalent Stage I larvae ranged from 5.531 x 105 for conversion factors derived from Lund and Stewart (1970 to 2 987 x'106 for conversion factors derived from Scarratt (1964). For conservatism, only the impact of the maximum estimated entrainment of equivalent stage I larvae for 1976 and 1977 i
1 obtained by applying ' conversion factors derived from Scarratt (1964) was assessed. Thic maximum entrainment estimate of equivalent stage I larvae was then equated to the nutber of adult l'obsters that would have recruited to the commercial fishery h j opproximately .5 years later.. 1 (
'Iha survival of stage I lobster larvae tatil they are recruited to the commercial fishery can be described _ by the equation (Ricker,1975):
G. 4-122
NEP 1&2 Nt = Noe-Zt s where: Nt = number of lobsters at time t No.= number of lobsters at time 0 i Z = instantaneous total mortality rate Saila and Flowers (1966) applied a similar model as described by the above equa tion
~
1
- to simula'te the ef fects of sex ratios and fishing regulations on a theoretical lobster i population.
. Wilder (1965) estimated that the -instantaneous rate of natural mortality (M) for lobsters I was between 10 and 15 percent. Since total instantaneous mortality is equivalent ~ to the sum of natural (M) and fishing (F) instantaneous mortality (Ricker 1975), and since , ]( Applicant assumed that F=0 during the time period prior to rect Jitment to the fishery. then an estimate of total mortality for pre-recruitment lobsters is approximately 10 1 to 15 percent. Applicant calculated Z-values for post-recruitment male and female lobsters Q81 mm i carapace length) from length-f requency data on the heavily exploited long Island Sound ! lobster fishery reported by Smith (1977). Age-frequency distributions for these data vere developed by applying the Von Bertalanf fy growth equation (Ricker,1975) derived
- by the Ithode Island Division of Marine Fisheries for lobsters from the mid-shelf region of Rhode Island Sound. The general f o rm of the Von Bertalanf f y equa tion is
l L g =L= [1 - e-K(t-to)j where: Lt = length at age t L. = mean asymptotic length j K = Brody growth coefficient i G.4-123 e
-m-g e-w - n =s w- _ m e gr*--m+* g -*.y w' y -79y '-~w-w-w tw-r1- - - --M-=
NEP 1&2 T = age in years ( t o = age at first egg extrusion , The coefficients for the above equation for Rhode Island Sound (mid-shelf region) male and female lobsters are (M. Fogarty, Rh o d e Island DEH, personal comm.) Male Female 1 = 280.784 L.= 240.020 K = 0.081 K = 0. 0 71 to = 0.179 to = -0.134 Based. on the above info rma tio n , the male post-recruitment survivorship and total instantaneous mortality coef ficients for the 1,ong Island Sound lobster fishery were calculated to be 0.115 and 2.160, respectively. Coef ficients for the Rhode Island post-recruitment male lobster stock (dtich are >78 mm carapace length) were assumed equivalent to those given above. ( Approximately 8%, 8% and 40% of female lobsters, 78, 81 and 89 mm long respectively, f rom Rhode Island Sound were found to .be gravid (M. Fogarty Rhode Island DEM, personal . comm.) For long Island Sound, these gravid female percentages for similar size females were approximately 20%, 21% and 24%. Dua to the dif ference in the minimum legal size (and therefore the time at wt.ich the female populations undergo fishing exploitation), and the dif ference in the f requency of berried females for the Connecticut and Rhode Island lobster fisheries, survivorship cad total instantaneous mortality coefficients for long Island Sound female lobsters were not directly applied to the Rhode Island females of age 5.4 years (approximate cga at minimum legni size) to 6 years (common age of females undergoing fishing cxploitation in both populations). Instead,, total mortality coef ficien ts fo r Rhode Island non-gravid female lobsters f rom age 5.4 years to 6 years were assumed equal to those determined for males in Long Island Sound (only about 8% of Rhode Island female G. 4-124
NEP 162 lobsters under age 6 are gravid) . For. gravid f emales (which are protected) within this age class, survivorship and Z was assumed equivalent to natural rates, or 0.86 and 0.15, respectively. Survivorship and Z for all Long Island Sound temale lobsters g reate r than or equal to 6 years (>85 mm carapace length) was 0 186 and 1.682, respectively. Coef ficients for the Rhode Island female lobster stock of the same age were assumed to be equal to those given above f o r Long Island Sound. Saila et al. (1969) provided the following regression equation for estimating f ecundity as a function of sioe: Log (Fecundity) = -1.6017 + 2.8647 log (Carapace length in mm) Utilizing the above information plus an assumed sex ratio of 1:1 for an unexploited population, and assuming no reproduction af ter 20 years, a Leslie population projection matrix was constructed (Table G.4.2-1) which described a stable population (the eigen ( ~ value or finite population growth rate was 1.00). In this model, the survival rate (So ) from larval stage I to age 1 was determined by a numerical method presented by Vaughan and Saila (1976) to be 5.951 x 10-5 Values significantly dif ferent from the value of S o will not allow the lobster population size to remain stable. A Leslie population projection matrix was also constructed for the heavily exploited Long Island Sound population to determine the magnitude of the density dependence in survivorship during the first year of life (So ) which would be required in order to maintain a stable population. In the exploited population. S was o 4.067 x 10 ~4 or a 6.8-f old inc rease in survivorship from larval stage I to 1 year of age over the unexploited population. This latt.er estimate of S was o used to project the number of adults not recruited to the fishery. In reality, it is not believed possible for there to be such great elasticity in S ,oand the following impact estimates are considered to be overly conservative. G. 4-12 5
N EP 162 i From these estimates of age-specific survival, approximately 7880 minimum legal-size lobaters would not be recruited to the fishery due to the estimated 1976 entrainment cf equivalent stage I larvae. For 1977, 628 legal size lobsters would not be recruited to the fishery due to entrainment. Krouse (1973) provided the following leng th-we igh t regression for lobsters in Maine Log W = -2 9052 + 2. 9013 Log L whore: W = we igh t in grams, and L = carapace length in mm From the above regression, a minimum legal-size lobster (78 mm) in Rhode island would weigh approximately 384 grams or 0 85 pounds. Th us , the total weight of lobsters not rceruited to the commercial fishery due to maximum projected 1976 and 1977 entrainment ( io cpproximately 6698 and 534 pounds, respectively. This represents 0.20% and 0 02% of the 1976 and 1977 Rhode Island landings, respectively. As c result of the above calculations, which indicate that the effect of entrainment on this species will be minor, it is concluded that the lobster population will suf fer to cppreciable harm as a result of entrainment. Total Impacts. The lobster is a highty thermal-tolerant species which will not be cubject to more than occasional entrapment. The one potential source of plant induc ed cffects on this species is entrainment. A conservative analysis of the number of adult lob:ters that would not be recruited to the commercial fishery due to estimated 1976 ccd 1977 entrainment of lobster larvau showed that the impact would be small compared to the commercial fishery; entrainment ef fects amount to a fractional percentage of th] Rhode Island landings. G.4-126
NEP 162 Consequently, Applicant believes that the operation of the heat dissipation system of NEP 162 will not result in ap p r ec iab le harm to the lobster population. 4.2.17 Eelgrass (Zostera marina) 4.2.17 1 Life History. Eelgrass is an aquatic spermatophyte with a worldwide d is t r ibu t io n. On the western side of the North Atlantic, this perennial ranges from as far north as Greenland (Lange, 1887) and liudson's Bay (Prosild,1932) southward to the Carolina (Se tchell,1920) . Areas of greatest abundance were found between the Gulf of St. Iawrence and North Carolina. Eelgrass may be found on a wide variety of sea bottoms; f rom which, through its root systems, it derives most of its nutrients (McRoy and Baradate,1970; McRoy and Goering, 1974). It may become established in a variety of substrates, ranging f rom sandy gravel to sof t mud . According to Burkholder and Doheny (1968), the most favorable bottom I appears to consist of fine muddy sand beneath a coarser layer of sand or mud . Eelgrass becomes established f rom the low tide mark seaward to a depth of 10-12 f eet. It is tolerant of a wide range in salinity, having been found living in f reshwater (0 ppt) and at 42 ppt (Short e t al . ,19 74 ); the optimum salinity range is 10-30 pp t (Phillips, 1974). It is also sensitive to light, as studies by McRoy (1966) havu ind ic a te d that photosynthetic activity reaches a maximum at about 25 langley / hour, liigh turbidity , resulting in severe light attenuation, would be detrimental to this species (Short et a l . , 19 7 4 ) . Crowth has been found to be stimulated by water currents up to 0 7 knots (Conover,1968). Burkholder and Doheny (1968) have desc ribed the development of Zontora in t.ome detail. They indicate that flowe ring shoots are developed dur ing the second year after G. 4-12 7
N E P 162 i garmination. Pollen is filamentous and is maintained in suspension by currents. Each f ruit produces a single seed, there being an average of 60 seeds per flowering shoot. Eelgrass may also extend its coverage through expansion of its rhizome system beneath tha sediment and subsequent emergency of new shoots. Eelgrass is periodically af fected by disease over large geographic areas, the last 00rious outbreak - termed the " wasting disease" - occurred around 1930. By 1934, cccording to Stevens (1936), approximately 90% of the eelgrass in Western Europe as well as of the Eastern United States has been destroyed. Eelgrass fulfills an extremely important role in areas such as Ninigret Pond, where it occurs in dense concentrations. It offers an ideal shelter, habitat and substrate for a variety of macro- and microinfauna. Studies by Alle (1923) and Stauf fer (1937) 12 the Woods Hole area revealed a 331 reduction in the number of species present af ter ( disappearance of eelgrass. In addition, dead and dying celgrass yields large amounts of nutritive material (Phrsha11,1970 ) and contributes, directly or indirectly, a high percentage of the food coterial for fish, shell f ish and wa te r f owl, a s well as f o r the mic rof auna. Because the root system of colgrass tends to stabilize otherwise shifting bottom, it helps to develop a suitable substrate for various valuable species of bivalve mollusks, including the hard clam and bay scallop. 4 2 17.2 Impacts of construction. Eelgrass is not present in the construction area in Block Island Sound. 4.2 17 3 Impacts of Plant operation. Because it la confined within Ninigret Pond and b:ccuse its' primary means of reproduction is vegetative (rhizomes), there will be no off ct of' plant operation on this species. G. 4-128
NEP 162
- 4. 3 Other Impacts Impacts other than those associated with entrapment, entrainment, and thermal' ef fects can occur due to plant operation. These impacts include of f ect of chemical and blocide discharges and indirect lethat and sublethat of fects as cold shock, gas bubble disease, skinny fish syndrome, pressure ef fects, and thermal Sackflushing. A discussion of these potential impacts is provided betw.
- 4. 3.1 Cold Shock The cold shock phenomenon occurs when organisms have become acclimated to high temperatures and are a,aldenly exposed , due to unit shutdowns, to low temperatures usually near or below their minimum thermal tolerance.
With an offshore multi-port diffuser system, the potential f or thermal shock dur ing ( shutdown or refueling is expected to be very small. Ref ueling or other scheduled shutdowns are normally planned such that only one unit is operative at a given time so that at least half the plan t's theriaal d isc ha rde will normally be present. Fu r the rmo re , the dif fuser reduces water temperature by rapid dilution. With the relatively low tanperature dif ferential throu,ghout those parts of the nearfield in which fish can maintain their position, it in unlikely that shutdown of one or both un its could result in significant thermal shock to aquatic biota because tempe r a t u r e rise is relatively slight in these areas. No physical boundaries exist at the discharge point for mobile organisms to orient into or be confined by, and it is unlikely that marine life can reside in the jets for more than a few necunds due to the discharge velocity and momentum of the dif f user jets. 'thus, the potential for significant cold shock impacts to occur at NEP 1&2 is judged minimal. G. 4-12 9
NEP 1&2 ( 4.3.2 Cas Bubble Disease Thstmal ef fluents supersaturated with dissolved gases can have detrimental ef fects on fith. Fish that are attracted to and subsequently reside in supersaturated ef fluent water for a long enough period will absorb more gas than can be maintained in solution in their bodies. When this gas comes out of solution within the fish, gas bubbles are formed causing a condition generally referred to as gas bubble disease. Gas bubble disease is a pathological process due to one or more physical manifestations including g:s emboli, exopthalmus, and systemic emphysema (Wolke et al., Bouck and Stroud,1975). In .a mild form, gas bubble disease may result in disorientation and erratic behavior.
. L2 its most severa form, however, it can result in death. Studies have also shown that fith can recover from the ef fects of short exposures to high levels of supersaturation if r.eturned to ambient levels.
( Incidents of gas bubble disease of fish in the thermal ef fluent of electric generating ctations have been reported by several investigators (De Mont and Miller,1971; Miller end De Mont, 1974; Marcello and Strawn,1972; Marcello,1975; Marcello and Fairbanks, 1976; Fairbanks and Lawton,1977). TVo of these reported incidents occurred at a New England coastal power plant (Pilgrim Station) and involved a species designated as a representative important species for NEP 1&2 (Atlantic menhaden). Each of the above reported incidents of gas bubble disease, however, occurred at power stations utilizing choreline, surface discharge systems. The likelihood of such incidents occurring at NEP.162 is greatly reduced due to utilization of a submerged multiport dif f user d ischarge. , Subterged dif fuser discharges promote rapid dilution of heated ef fluent with cooler ambient water. TVo parameters control saturation levels of games in the water as it ; exits f rom the underwater dif fuser and mixes with the ambient water. These parameture are hydrostatic pressure and thermal dif fusion characteristics of the dif f uner. 1his G. 4-130
1 NEP 1&2 interaction of temperature and pressure on the gas solubility of seawater as it passes , 1 through a power plant dif fuser cooling system was examined by Kircello, Krabach and Ba r tle t t (1975). These authors plotted the gas saturation history of a parcel of seawater through a dif fuser system for the conditions of a 37"F temperature rise, and
\
intake water temperature and gas saturation of 400F and 110% saturation, respec tively (typical of surface conditions at coastal sites in this region). The dif f use r they evaluated was designed to meet a surface temperature criteria of 5"F above ambient. They pointed out that since the circulating water absorbs heat on passing through the cordenser, the percent saturation of dissolved gas increased to about 1601. The highly cupersaturated water is pumped to the dif fuser located at a depth of 30 f ee t where the caturation becomes less than 90%. As the heated water is discharged f rom the dif f user nozzles and rises to the surface, temperatures are a ttenua ted and the hyd routa tic pressure decreased such that the of fluent gas saturation is slightly above 115% at the l curface. Ibsed on attdies of the tolerance of a variety of fish to gas supersaturated conditions, regulatory agencies and other technical advisory groups have estabitshed that a 1151 saturation surface criterion would provide reasonable protection to fish f rom gas bubble disease mortality (USEPA,197 7; Rulif son and Pine, 1976). Since the NEP 162 circulating water system utilizes a submerged dif fuser which disch1rges between the 30 and 40 foot depth, and is designed to meet a maximum surf ace temperature c riteria of about 6"F above ambient, gas naturation leveln will be only slightly above ambient intake levels. Ibrthermore, an of f ahore submerged dif f user has been shown to be a technically feasible solution to the problan of gas bubble disease mortality at Pilgrim thiclear Power Station, Marcello et al. (1975). Th us , the potent in t for gas bubble disease to occur in the vicinity of the NEP 1&2 thermal discharge is greatly reduced and should cause no significant impact. G. 4-131
NEP 1&2 433 Hyd rostatic Pressure Ef f ects The proposed NEP 162 intake system will utilize a bedrock tunnel at a depth of about 460 to 200 feet to convey cooling water to the site (see Section 3.0). As a result of this depth, entrapped organisms will be subjected to substantial hyd rosta tic pressures. These pressures (directly or indirectly) could cause such adverse ef fects to entrapped biota as gas bubble disease, pressure related mortality, or meenanical (brasion along the tunnel system due to altered buoyancy from gas bladder compt saton. A detailed evaluation of the potential for pressure related impacts is provided in f.R Appendix I. This evaluation was based on a review of existing literature and powe r plant operating experience on the survival of fish and other organisms exposed to various pressure regimes. As a result of this study, it was concluded that of the concerns expressed above, only the potential for increased mechanical damage due to abrasion with the intake tunnel walls may occur. While it is not pos s ib l e to quantify this potential increment ef fect, it was speculated that f actors such as the development of a laminar boundary layer and the possibility for increased swimming activity of fish when pressurized may tend to minimize this ef fect by keeping fish in the mainstream of the water flow. The potential for gas bubble disease or gas bladder rupture to fish was shown to be minimal at NEP 1&2. Pressures of the magnitude experienced by (ish during passage through the proposed NEP 1&2 intake tunnel system was also shown to have a low potential for adverse impact. Th us , the overall potential for adverse impactu resulting f rom exposure to hydrostatic pressures during transit through the proposed NEP 162 intake tunnel system is judged minimal and should cause no appreciable harm. 434 Skinny Pinh Syndrono Loss of wight and ultimately a corresponding reduction in the roetlicient at condition, or " skinny f ish synd rome" is alluded to in Kircy (1916) . Possible reasons f o r lona G.4-132
NEP 1&2 l of height and condition for fish is attributed to: (1) an increased metabolic rate restd. ting frca prolorged exposure to an increased temperature environment; (2) a greater expenditure of energy for fish species to maintain themselves in the discharge plume; and (3) overcrowding resulting in increased competition for food. l Of particular importance in understanding this phenomenon and trying to make projections specific to Applicant's thermal discharge system, is that " skinny fish synd rome" is l Such l reported at a power station which utilizes a shoreline, surf ace discharge system. a discharge design encourages finfish to take up residence within a confined area for ! extended periods of time for example over the winter. The likelihood of finfish developing similar symptomatic conditions reported at the Connecticut Yankee nuclear generating f acility (Marcy,1976) which utilizes a shoreline discharge, is considered remote since Applicant proposes to use a submerged multiport i l( dif f user discharge system. A dif fuser system is designed to enhance the mixing and dilution of the heated discharge. The thermal plume which result s is dynamic in nature and is always in a state of transition as it responds to constantly changing ambient reversing tidal currents, wind, and wave action. Consequently, continement within a restricted area where fish become acclimated and ultimately develop such secondary ef fects as " skinny fish syndrome" is not anticipated. 4.3 5 Premature Spawning The sequence of events rel'ating to maturation, spawning migration, release of gametes, and subsequent development of egg and embryo represents a complex interaction of input stimuli. Ano:M the environmental f actors are light (photoperiod), temperature, salinity, water currents, tidos, and food abundance which are all seaminally related one way or l another. On the whole, there appears to be a more pronounced relation between light, Ilowever , one of particularly where precision of timing and migration are involved. l G.4-133 l t
NEP 163 the reasons for this precision may be the need imposed by a restricted temperature range ( for early development. In general, temperature may affect the rate of maturation; it is known to act as a timing and/or releasing factor; it undoubtedly imposes a marked confining ef fect on reproductive limits (Breb,1970). Obviously, since temperature is an influential f actor in spawning, any direct alteration to background anbient tmperatures (such as the addition of waste heat) has the potential of inducing premature spawning activity. Inasmuch as electric power plants introduce waste heat into the environment there must be delineating parameters which enhance the potential for pranature spawning. One such para:neter is a shoreline discharge structure which enables organisms to orient to the discherge plume with its rather stable isothermal areas over an extended period of time. One particular case in point is IPA's reference to a premature spawning incident in the shoreline discharge canal of Brayton Poin t (US EPA, 19 7 7 ) . ( 1he possibility of a similar incident occurring at NEP 1&2 is considered remote since a submerged multiport dif fuser will be used versus a shoreline discharge structure. Design characteristics specific to a dif fuser discharge system enhance rapid mixing and subsequent dilution of the thermal plume. The se factors, when combined with the dynamic nature of the discharge caused by '.idal fluctuations, wind and waves does not allow aquatic organisms to orient themselves to a preferer tial isotherm for an extended period of time. Consequently, any possibility for premature spawning is considered min imal . 436 Ef fects of Chemical _ and Blocido Dischargen To prevent biofouling in the circulating and service water systems, a combination of chlorine, antifoulant coat ings, and heat treatment wlL1 he utilized. Fuuling cuntrol in the circulating wa ter system will be conducted one unit at a time in order to G.4-134
NEP 1&2 eliminate the possibility of additive ef fects. A f ull discussion of the fouling control systans is presented in Section 3 4, 3 4.2 and 3.6.1 of the 12. Oslorination of t_he circulating water system will comply with the EPA regulations Witch requires a maximum average free available of 0 2 ppa for two hours per day per unit with an instantaneous maximum of 0.5 ppa. Adherence to these regulations will result in minimal environmental impact. Because equipment temperature requirements prohibit heat treating the service wa ter system, and because the pipes of this system are too small to be painted, the service water must be continuously chlorinated. Chlorine will be injected at a rate which will result in a discharge concentration of 0.2 ppa f ree available prior to mixing with the circulating water. Upon mixing with the circulating water there will be an immediate dilution of approximately 18:1. In' addition to dilution, the circulating water also g provides a new chlorine demand. 'Ihis dilution, then, will etfectively dechlorinate all of the free available chlorine in the service water, and it is unlikely that any chloramines will be formed af ter the mixing. Because of the low volume and great dilution of this flow, it is believed that any incremental mortality caused by continually chlorinating the service water will be insignificant. Since all organisms will probably be killed when subjected to the 370F At , chlorine induced entrattunent mortality may be considered to be zero. Beeausa the circulating wator pumps provide ilow in only one direction, the pumphouse, on-site circulating water pipes and the inlet water boxes will never be heat treated. As intermittent chlorination has proven inetfactive in the control of the fouling organtsra of primary concern (the blue mussel Mytilus edulis), it will be necessary to coat these components with an antifoulant coating. The concentration of leached toxic material f rom these coatings will be extremely naall and should not adversely af fect C. 4-13 5
NEP 162 bista in or beyond the plant discharge. A d:scription of the chemical treatment system is found in ER Section 3.6. ' All chemical discharges will conform to applicable regulatory standards. No adverse ef fects on the marine biota are anticipated. 437 Ef fect of Thermal Backflushing As discribed in Section 3.3, thermal backflushing is used to control biofouling in order to maintain the cooling system in an operational condition. For heat treatmen t~ to be effective Applicant estimates that a backflush discharge temperature of 1200F (490C) is required for approximately two hours per treatment. Esckflushing heat treatment is expected to be required about once every two weeks during th3 warmer months between April to November and less -f requently during other months. Depending on the ambient water temperature, a backflush temperature of 120 F (49 0C) f represents a A T of f rom 50 to 830F (28 to 460C). Resultant plume ef fects are incurred primarily by the more passive plankton which are entreined into the backflush discharge. On the other hand, the nektonic species, such no fish and squid could avoid any deleterious thermal ef feet as a result of their cwimming ability. Steilarly, benthic organisms are not expected to be ef facted since ths backflush plume never touches the bottom. Hect shock resulting from the high A T of the et fluent wa ter will cause localized mortality among organisms unable to avoid the backflush plume. The number of entrained planktonic organisms is small, however, because of the reduced volumes of cooling water required as a consequence of the corresponding high AT. C. 4-136
NEP 1&3 5.0 ALTERNATIVE INTAKE SYSTEMS he proposed intake systen has been described in Section 3 of this appendix. D e purpose of this section is to_ summarize considerations of alternative intake systems. As discussed in NEP 1&2 ER Sections 3.4 and 10. 2, three alternate intake system concepts wre evaluated. These are: a cotwentional onshore intake b.. submerged of fshore intake located at 30 foot depths
- c. submerged far offshore intake located at 50 foot depths.
ER Appendix H describes the decision process used in selection of the proposed intake. Figure G.5.0-1 depicts this decision process and provides references to appropriate , sections of the ER. 5 1- Onshore Intake 5.1.1 System Desc ription he onshore intake system is described in ER Section 10.2.2. For this system, an ocean front intake is located on East Beach where flow is drawn through bar racks into the intake forebay. Sheet pile extends of fshore about 400 feet to form an intake canal. . Cooling water flows to the pumphouse at the plant site through one 18 foot (1.D.) in take tienel 3700 feet in length. 5.1 2 Envirormwntal' Impacts Construction impacts of the onshore intake system are greater than those associated ( with the proposed of fshore intake system. Open cut excavation and dredging is required C. 5-1
m NEP 162 on East Beach and in the nearshore zone whereas similar activities are not required for construction of the proposed intake system. Entrapment and entrainment impacts associate'd with' the onshore East Bearch intake. are judgtd to be similar to the proposed of fshore intake. However, there are no thermal ef fsets of backflushing for the onshore intake because chlorination is used to control biofouling control. Resource utilization and aesthetic impacts are greater for the onshore East Beach intake. It -rsquires the use of East Beach and may interf ere with small boat traffic. The proposed of fshore intake requires no use of. East Beach, doe's not af f ect small boat traf fic and has no visib.le components. 5&1.3 Engineering Considerations Engineering and ec'onomic considerations clearly f avor the onshore intake system. Its I procent value .(1985 dollars) is estimated to be'$11 million less than the proposed of fshore intake. It can be constructed using primarily land based equipment and conytntional construction techniques. Geotechnical considerations also favor the onshore intake because the tunnel riser shaf t can be fabricated on shore and in shallower ovsrburden. 5.1 4 Summary: Onshore vs. Offshere Intake . A broad evaluation of the foregoing environmental and engineering considerations, led to the selection of the of fshore intake concept in preference to the onshore in take . In gsneral, engineering factors. favor the onshore intake; however, the environmental bensfits of the of fshore intake are considered suf ficient to justify the additional ccet and engineering disadvantages. ,s
, G.5-2
NEP 162 5.2 Far Of f shore Intake 5.2.1 System Desc ription The alternate of fshore intake system is described in ER Section 10.2.3. It consists of two identical of f-se t submerged intakes, two 14-foot inside diameter in take pipes connected to one 18-foot inside diameter intake tunnel through associated riser shaf ts, and a pumphouse located on the site. The intakes are located at a water depth of about 50 f t in Block Island Sound approximately 10,000 feet south of the plant site. Tunnels would extend out an initial 6000 feet from the site followed by an additional 4000 feet of pipe. This intake system is estimated to cost $60 million (present value - 1985 dollars) more than the proposed in take system. 5.2.2 Env iro nmen ta l Impacts { Construction' effects of the far of fshore intake are greater than for the proposed of f shore intake. This is because cut and fill pipe installation is probably required to extend the cooling system beyond the 30 foot depth contour. Entrapment and entrainment impacts vary by species for the proposed and far offshore intake location. Although the far of f shore intake accounts for a small reduction in annual average entrainment of ichthyoplankton, it results in an increased entrainment of eggs and larvae of six representative important species as compared to the proposed intake. . Of these six RIS exposed to greater entrainment by the far offshore in take , five are commercially important spec ie s ( i.e . , Atlantic menhaden, silver hake, scup, Atlantic nackerel and butterfish) which contribute to the economically important Rhode Island of fshore commercial finfish community (NEP 162). Although the predicted absolute number of entrained and entrapped individuals varies by species for the proposed and far offshore in take locations, there is no practical G.5-3
r NEP 1&2 justification for selecting the far of fahore intake. As demonstrated by Section 4.2 e cf this Appendix, the overall impacts attributed to the proposed intake are negligible. Consequently, relocating the intakes farther of fshore in an attempt to further minimize tn already negligible impact is neither cost ef fective nor could it have any measurable envirornental benefit. Tha aesthetic impact of the proposed and far of fshore in take locations are similar. In neither case will any structure be visible after construction is comple te . In both cases, the quantity of backflush flow and temperature rise are similar; cc::equently, thermal ef fects of backflushing are also similar for the proposed and fer of fshore intakes. 5.2 3 Engineering Considerations (' Engineering considerations favor the proposed intake location. It is anticipa ted that cut and cover pipe installation is required to extend the cooling system beyond the 30 foot depth contour. This results in construction problems not encountered in fchrication of bedrock tunnels which extend to the proposed intake location. Furthermore, placanent of the intakes at the far ofishore location requires construction activity in deeper water ditch is also a disadvantage. Tha additional $60 million cost (present value-1985 dollars) of the f ar of f shore intake 10 clso a disadvantage. This increased cost is incurred primarily due to the addition of two 4000 foot lengths of 14 foot I. D. p ipe .
5.2.4 Summary
Proposed vs. Far Of f shore Intake It has been demonstrated that the environmental impacts of the proposed intake system i cro negligible (Section 4.2 of this appendix ER Section 5.1). Fu r the rmo re, it is unlikely that any not measurable environnental benefit can be derived by relocating C. 5 -4
NEP 162 the intake farther of fshore. In fact, for at least five commercially important species, the far of fshore intake location incurs greater entrainment impacts. Even if there were a theoretical environmental benefit to relocating the intake farther of f sho re, it could not be -measured because the impacts of the proposed intake are ned l igible. Incurring an additional cost of $60 stillion to relocate the intake far of f shore is wholly disproportionate to any potential' environmental benefit to be gained. In fact, it is
.likely -that the impact on certain important species would be increased by relocating the in take far of f shore. harthermore, construction impac ts would be substan tially increased.
The proposed intake systern is believed to be feasible from a construction and engineering perspective. . Its cmt, although excessive in comparison to a conventional onshore intake system, is believed to be commensurate with its environmenta l b ene f i t s . I , 0 5-5
NEP 1&2 6.0 REPRESElfrATIVE IMPORTANT SPECIES IMPACT SUMMARIES AND MASTER ECUSYSTEM RATIONALE ( C2 cise summaries of predicted impacts on the NEP 1&2 Representative Important Speciels cro presented below in Section 6.1 and are summarized in Table G.6.0-1. In addition, Section 6.2 provides the master ecosystem rationale that integrates biological, physical , cud plant operational data to demonstrate that construction and operation of NEP 162 will not cause appreciable harm to the aquatic ecosystem of Block Island Sound, and thus will assure the protection and propogation.of the balanced indigenous population of shellfish, fish, and wildlife in and on Block Island Sound in the vicinity of NEP 1&2. 6.1 Representative Important Spacies - Impact Summaries With the exception of construction effects, impacts of plant operation (i.e., entrapment, thermal, and entrainment ef fects) are given below for each Representative Impo r tan t { Species. Because of the general nature of Applicant's construction impact assessments,
~
ccontruction effects for all species are addressed together in Section 6.1.1. 6.1.1 Impacts of Construction: Negligible. Ba-is for Prediction: Twelve of the Representative Important Species are free swimming cpecies. 1he temporary increases of suspended sediments and turbidity in the immediate cros of the offshore construction will not af fect juveniles or adults as they are sufficiently mobile to avoid such occurrences. There may be some adverse af f act on cgg and larval forms, but because of the transitory nature of the construction af fects and the relatively small tubers of eggs and larvae in Block Island Sound, no appreciable impact is expected. No cdult hard class were found in Block Island Sound and larvae were sparce. S:nd shrimp (Crannon _septemspinosa ) and adult lobster (flomarus americanua) are 0.6-1
NEP 1&2 suf ficiently mobile and sediment tolerant such that no appreciable impact will occur. 6.1.2 Atlantic menhaden (Brevoortia tyrannus) Entrapment Effects: Neg lig ib le . Basis for Prediction: Based on the comparative evaluation study of menhaden and their ecological counterparts at f acilities with velocity cap intakes, Atlantic menhaden were judged to have a medium to high po tential f o r entrapment. However, t acto rs we re identified which would tend to minimize entrapment of this species at NEP 1&2. These factors included the wariness of adults which may cause them to avoid the intake structure, the young remain in the estuary much of the time and would not be available for entrapment, and the lack of entrapment of this species and others of the same genera at the operating velocity cap intake at St. Lucie Generating Station in Florida. To , place any potential menhaden entrapment losses at NEP 1&2 into perspective, modeling results on the population impact to menhaden resulting from entrapment at two nearby coastal power stations were evaluated. Modeling results from these nearby facilities indicated that within the range of annual intake entrapment losses of 1000 menhaden to 210 million menhaden (the larger number being derived f rom a mortality coet ticient over 1700 times larger than nonnally expected), no significant impact occurred to the Atlantic menhaden population. Since any projected entrapment loss of menhaden at NEP 162 would probably fall on the low side of the range of losses cited above, i t wa s concluded that entrapment of menhaden at NEP 1&2 should cause no appreciable harm to the Atlantic menhaden population. Thermal Ef fects: Negligible. Ihsis for Prediction: Thia impact is predicted on the basis of the Applicant's thermal assessment model which integrates background hydrographic data, plant thermal discharge parameters and published literature petrtaining to the s pe c ie s' life history / thermal G.6-2
4 NEP 1&2 tolsrance characteristics. t l Such a thermal tolerance assessment indicates rather conclusively that the NEP 1&2 thornal discharge should not have an appreciable impact upon this species. The NEP " 1&2 thermal discharge may interact with this species nearshore activities anytime during
' lata s'p ring or early f all. During this period, the various life history stages of this Based upon j
species could experience surface water temperatures between 53 to 75 F. the results obtained by the various investigators cited, such a temperature range falls wil within the temperature tolerance capabilities of this species.
- Entrainment Ef fects
- Negligible.
i Banis for Prediction: Larval entrainment losses were compared to those predicted to . Pilgrim-occur for Pilgrim Station Units 1 and 2 and Millstone Station Units 1, 2 and 3 Station, which would entrain 4.5 times more larvae than NEP 162 was predicted ' to ( conservatively cause a 0 00275 percent reduction in menhaden population over 50 years. 1 A predicted 0.08 to 1.1 percent reduction in
- Ne menhaden population af ter 50 years was calculated for Millstone Station using an intentional overestimate of inplant cortality. The estimated number of larvae entrained at Millstone Station is over 1.2 Thus , the
. tires greater than the number of larvae predicted to be lost by NEP 162.
Atlantic menhaden population would not auf fer appreciable harm as a result of larval 1 sntrainment.- 6.1 3 Bay Anchovy (Anchoa mitchilli) Entrapeent Ef fects: Negligible. Es*is for Prediction: Based on the camparative entrapment study, bay anchovy were judged to have a medium to h'igh entrapment potential. However, life history characteristics i of this species indicates that it is primarily an estuarine species using the upper 1 4 G.6-3
NEP 1&2 estuary as a nursery ground. Th us , the location of the intake is not in an area of preferred habitat. Furthermore, design development studies conduc ted f o r Southern California Edison on the velocity cap indicates that entrapment of the northern anchovy were substantially reduced. Thus, based on documented life history characteristics and velocity cap intake design, no appreciable harm to the anchovy population is an tic ipa ted . Thermal Ef f ec ts: Negligible. Basis for Prediction: Applicant predicts no appreciable impact upon this species resulting from the NEP 1&2 thermal discharge. Such an assessment is based upon the Applicant's integration of existing thermal tolerance literature, the species life history characteristics and predicted plant operating parameters. Similar to the Atlantic menhaden, the bay anchovy is an ubiquitous species which is I customarily associated with warmer water temperatures. Results generated from the Applicant's thermal tolerance analysis of bay anchovy eggs, larvae and adults indicates that these various life history stages should satisf actorily tolerate induced surf ace water temperatures predicted to range between 53 and 750F. Entrainment Effects: Negligible. Basis for Prediction: Stone and Webster Engineering Corporation was commissioned to conduct an entrainment assessment for anchovy. Using 1974 field data, they estimated the annual loss of 9.919 x 106 eggs and 6.064 x 10 8 larvae. These values, using a series of conservative assumptions, result in a prediction of an annual loss of 7 x 106 adults. Applicant us'ed slightly dif'fe' rent calcul'ation methods and estimated annual losses of 6.08 x 10 6 and 6.03 x 10 6 adults for 1974 and 1975. field data, respectively. It is concluded that Block Island Sound (BIS) is not particularly importan t to this C.6-4
NEP 1&2 specits as a spawning area considering the relative abundance of anchovy ichthyoplankton in BIS versus other coastal estuaries such as Narragansett Ba y . Given that the area , has comparatively low ichthyoplankton numbers, it follows that the adults lost also i~ ccustitute a small portion of the population. Applic an t , therefore, concludes that thare will be no appreciable harm associated with the entrainment of this species. i 6.1.4 Silver Hake -(Merluccius bilinearis) Entrapment Effects: Negligible. Bacis for Prediction: Based on the comparative entrapment life history evalua tion, oilver hake',~ particularly small hake, were judged to have a low to medium entrapment i potential. Whatever entrapment that may occur, however, is expected to have an 4 insignificant impact on. the silver hake population due to its relatively low abundance I in the proposed intake location, and its reported' high sw'im ~ speed capability. Furthermore, no entrapment of its ecological counterpart, the Pacific hake, has been 1 Therefo re, no' l recorded at operating velocity c'ap intake s in southern Califo rnia. r bignificant impact to the . silver hake population is expected. Thermal Effects: Possible temporary ef fect to eggs and larvae. 2 Bseis for Prediction: Basis for such a prediction is predicated on the Applicant's r
-analysis of ~ existing thermal tolerance lite ra tu'r e , the specie s 1,1f e history characteristics and known, plant discharge design' parameters.
Making a conservative assumption that both the eggs and larvae cannot tolerate induced temperatures above those observed by the pplicant and cited in the literature, .then thsse particular life history stages could be af fected by the discharge plume at the and of its spawning'seacon. It should be emphasized, however, that the egg and larval
~
( dsnsities collected in Block Island Sound are comparatively low when compared to such i 1 4 G.6-5
NEP 1&2 areas as the Gulf of Raine. When this factor is combined with the small surf ace area influenced by the b F induced maximum temperature rise ( i .e . <1 acre) overall impac t is considered minimal . Any impact to the adult is expected to be negligible due to spe c ie s' strong swimming ability and dynamic nature of the discharge plume. Entrainment Effects: Negligible. Basis for Prediction: Using field data from 1974 and 1975, Applicant calculated the loss of 3 054 x 107 and 1 108 x 108 eggs, respectively. Larval losses would have been 8.614 x 105 and 4.281 x 10 6 , respectively, f or the same two years. These values represent the conservative loss of 332 and 1,413 adults for 1974 and 1975, respectively. If only spawning females were considered, then the 1974 and 1975 entrainment projections equate to the loss of 166 and 707 adults, respectively. Th us , the number of silver hake that would have developed frca 1974 and 1975 entrained eggs and larvae is equal to 0 006% and 0.02% of the 1975 Rhode Island, commercial silver hake landings (5,347,000
~
pounds). Also, the equivalent loss of gravid Temales for 1974 and 1975 would be 0.003% and 0.01%, respectively, of the same landings da ta . It is, therefore, evident that the impact of entrainment on silver hake will be insignificant. 6.1.5 Striped bass (Moros saxatilis) Entrapment Effects: Neg lig ib le. Basis for Predic tion: Results from the comparative entrapment evaluation study identified several factors which indicated . that striped bass are not candidates fo r significant entrapment. These factors included the minor entrapment of the ecologically similar species, white seabass, at operating velocity cap intakes in California, the absence of striped bass less than 12 inches in the site area, the high swim speed G.6-6
NEP 1&2 ctpability of this' species, their seasonal occurrence, and their close distribution ( inshore for a relatively short time. f Thermal Ef fects: Negligible. A Basis for Prediction: Thermal impact assessment evaluating the striped bass is based on the results generated from the Applicant's thermal impact assessment model which
. integrates : (1) the species' life history characteristics; (2) background hydrographic dtta and . plant operating paraneters, and; (3) published literature of the species thermal
, tolerance characteristics.
Such an analysis demonstrates the striped bass should be -able to interact with the Applicant's thermal discharge with no apparent detrimental ef fects. During the six to seven month interim when the striped bass is known to inhabit Rhode Island waters, 1
& saxatilis could encounter an induced surface water temperature ranging f rom a low of 530F to a high of 750F.
( Based on existing literature such temperatures fall well i within the thermal tolerance capabilities of this species. Inasmuch as spawrting and juvenile development up 'to two years of age only takes place in more southerly waters, the plant discharge will in no way, interf ere with striped. bacs egg, larval or early juvenile development. I Entrainment Ef fects: None. Bacis for Prediction: No striped bass. ichthyoplankton have been found in the study
. area, therefore, there will be no entrainment related losses.
6.'l.6 Bluefish (Pomatomus saltatrix) i Entrapment Effects: Negligib le. l Bacis f~or Pred ic tion: Results from the comparative entrapment evalua tion study G.6-7
NEP 1&2 identified several factors which indicated that bluefish are not candidates fo r
. significant entrapment. . These factors included the lack of impingement of this species s
by the operating velocity cap intake at St. Lucie, Florida (even though yearling bluefish are present throughout the winter), the high swim speed capability of blue fish, and that they are seasonal in occurrence at the proposed site thus being available for entrapment for only about four months of the year. Thermal Effects: Neg ligib le . Basis for Prediction: Results obtained f rom the Applicant's thermal assessment model form the basis for such a prediction. Such an analysis demonstrates rather conclusively tha t this species would be very tolerant of any induced temperature change res'ulting f rom NEP 1&2 ope ration. I Any thermal discharge / organism interface will involve the juvenile and adult life history-stages only. During the six to seven month' interim in which blue f.ish are known to inhabit Rhode Island waters, h saltatrix could encounter a plant induced surface tanperature range from a low of 58 F to a high of 75 F. Integratioa of such temperatures with the species known thermal tolerance characteristics indicate such induced temperatures are well within the' tolerance limits of the bluefish. En trainmen t Ef f ec ts: No'ne Basis for Prediction: No bluefish ichthyoplankton have been..found in .the study area, i therefore, there will be no entrainment related losses. Scup (Stenotomus chrysops)
~
6,1.7 Entrapment Ef fects: Possibility of some entrapment, however, overall ef fect considered anall. G.6-8
NEP 162 i Bacis for Prediction: Based on factors -identified during the comparative entrapment evaluation study, scup were not judged candidates for significant entrapment especially during daylight hours since they are strong swimmers, they tend to be closely associated with the bottom during daylight hours, they are exceedingly wary fish, they have not bun entrapped in significant numbers at conventional shoreline intakes, and they are not particularly abundant in the location of the proposed intake. Because of the lack of data, en trapmen t of scup during the dark hours is dif ficult to predict. Thermal Effects: Minimal. Basis for Prediction: Scup life history characteristics in conjunction with: (1) known hydrographic and plant operating parameters ; and , (2) ava'ilable thercal tolerance -l i t'e r a t u r e form the basis for this species' thermal impact assessment. I Relatively low densities of scup eggs and larvae were collected in ichthyoplankton samples suggesting that this area of Block Island Sound is not a particularly f avorable spawning area. Such low egg. and larval densities when coubined with the species' preference of warmer spawning temperatures, indicates a small potential for thermal inpact resulting from plant operation. Similar to the earlier life history stages of this species, the anticipated thermal impact upon the adult is. also considered small ' duS to, the scup's ability to move from an area should it prove unsuitable, and its .zo: geographical temperature range which is known to exceed those induced temperatures ratulting from plant operation. Entrainment Ef fects: Negligible. Ba cis for Prediction: If NEP 1&2 had been operating at full Load during the period wh:n scup eggs and larvae were present, 2.946 x 107 eggs and 2.169 x 10 6 larvae would 8 havm been entrained in 1974. During. 1975,1.299 x 10 eggs and 7.429 x 10 6 larvae would G.6-9
NEP 1&3
- have been entrained. Illing conservative estimates of fecundity and egg-to-larval ratio, the larval entrainment in 1974 and 1975 would have been equivalent to 3.36 x 10 'and7 1.15 x 108 eggs, respectively. Based on the total spawning life fecundity, the predicted egg and larval entrainment, and the assumption that only two sexually mature scup will develop f rom the lifetime spawn, the entrainment by NEP 1&2 during 1974 and 1975 would have resulted in a loss of 3,360 and 13,100 scup, respectively.
Applicant thus estimates that the amount of scup potentially lost due to entrainment in 1974 and 1975 is equivalent to 0.08% and 0.3%, respectively of the average 1971, 1973 and 1975 Rhode Island commercial scup landings, based on an assumed weight of 1 pound per fish lost. 6.1.8 Cunner (Tautogolabrus adspersus) Entrapment Effects: Neg lig ible. ( Basis for Prediction: Based on the comparative entrapment evaluation, cunner were judged to have a low to nedium entrapment potential. However, several f actors were identified that would indicate that entrapment of cunner should not be significant. These factors indluded the low entrapment of its. ecological counterpart, opaleye, by velocity cap
- g intakes in California, its inactiv(cy at night, its unavailability in the winter, the t6ndency for larger cunners to inh bit water deeper than that at the proposed in take location, and that cun n e r s a :Ie we ll ad apted to wave surge conditions.
1 Tn e rm a l Effects: Minimal. Basis for Prediction: Th'.s impact is predicted on the basis of thermal tolerance data Y for this speciec integratyd with known biological, hydrographic and plan t opera ting
,' I parameters to produce a tfiermal assessment model.
g i Such an analysks indicates that f rom a temperature tolerance standpoin t the cunner I c.6-10
NEP 1&2 appears to be a ha-dy species. Based on the literature, the cunner can tolerate i i temperatures as high as the mid to upper seventies during the colder months and ~the cid-eighties during the warmest summer conths. Such a tolerance level makes the cunner -
~
.f well suited to withstand the maximum induced temperature rise of' boF within the boundary
, of the- mixing zone.
Fatrainment Effects: Negligible. Basis for Prediction: Stone and Webster Engineering Corporation-was commissioned by - i Applicant to analyze potential entrainment. losses on the local cunner po'pulation. A density-independent eigenvalue model which incorporates a leslie population projection matrix was used. Using several very conservative assumptions, the net ef f ect ~af ter ] 40 years of continuous operation at 100% load (approximately 80% load is expected) would be a 3.03 %' reduction in population size. 6.1.9 Sand Lance (Ammodytes 'anericanus)
-Entrapment Effects: Negligible.
danis for Prediction: Based on existing information on this species' abundance and di'atribution in the study area, plus such factors identified during the comparative
- entrapment evaluation study as its preference for water over unobstructed sand bottoms, its failure to be attracted to reef-like structures, its apparent exceptional night-ti
- :.e vision, and its sporadic and sometimes lengthy sojourns into bottom substrate thereby reducing its entrapment availability, it was judged unlikely that sand lance will be entrapped in large numbers. *
! Th'armal Ef fects: Possibility of some thermal ef fect. j Banis for Prediction: The integration of published thermal tolerance literature and , ths species' known life history characteristics form the basis for the thermal impact G. 6-1 1 r
- . , , . , , , m. , , - , , - . . , , - , -.- -,_-..,,----,y... , , , , , , - _ , . - - , . . , _ . , . _ _ . . - - , , , , . . . , ,-,,c-,,,, . . - . . - . - . , , _ - ,
i NEP 1&2 a ssessmen t. Existing thennal tolerance information indicates that a 60F induced temperature increase could possibly af fect the. egg and larval stages of this species. . Adults, of course, i l are able to choose their preferred temperature and will not, reside in the plume. It i ' should be pointed out, however, that any area of exclusion would be relatively small . j when compared to the total habitat area where sand lance could-exist. Entrainment Effects: Neg lig ib le Basis for Prediction: Eggs of the sand lance are demersal an.d adhesive thus entrainment will not af fect this life stage. f I During 1974-1975 and 19 75-1976, larvae were present in.the site area'for 194 and 218 days, respectively. If the plant were operating at 100: load, an estimated 1. 763 x
,q 10.8 and 4.577 x 107 larvae would have been entrained during 1974-1975 and 1975-1976, respectively. Using conservative assumptions, Applicant estimates that betwee'n 43,000 and 8,300,000 adults would have been lost annually during those years. This equates to between 22,000 and 4,150,000 females whose spawn would be lost.
The 4,150,C00 would weigh approximately 19,920 kg while the 8,300,000 lost adults would weigh approximately 41,915 kg. Thus, the annual loss to- the population can be viewed as negligible when considering that the European fishing fleet have reported the catch rate of between 2500 kg per hour and 15,000 kg per hour' of their sand lance fishery.
- 6.1.10 Atlantic Mackerel (Scomber scombrus) l Entrapment Ef fects
- Neg lig ib le .
i Basis for Prediction: Based on the comparative entrapment evaluation study, Atlantic , mackerel are not considered serious candidates for entrapment for the following reasons. l 1 l ! G. 6-12 l
.___. . . , _ _ . . . . . _ _ . . _ . - . _ . . . . _ . _ , _ _ . , . ,. _ _ . . _ _ , _ , _ _ , . ~ , _ - _ . . _. _... ,. _ . _ _ , _ ,
NEP 1&2 Its west coast ecological counterpart, the chub mackerel, is rarely entrapped by ' operating velocity cap in take s. Atlantic mackerel are fast swimmers, quickly become visually oriented, grow rapidly, and as yearling fish are in the area of the proposed intake only in-June and July. Thus, no appreciable harm is expected to occur to ' the Atlantic mackerel population. Thermal Effects: Possibility of some thermal ef fect. Basis for Prediction: The thermal impact prediction for this species is brised on the Applicant's evaluation of the thermal impact assessment model. Available thermal tolerance literature indicates the Atlantic mackerel is more of a cold water oriented species; consequently, the possibility exists that the various life history stages of Scomber scombrus will interact with the discharge plume. As a consequence of the mackerel's affinity for lower water temperatures the possibility ' ( of some thermal ef fect is anticipated. The likelihood of appreciable impact is considered remote, however, based on: (1) the adult's ability t'o select its preferential teaperature as a result of its swimming ability; (2) the increased abundance of eggs and larvae further offshore relative to the proposed discharge area; and, (3 ) maj or spawning and larval life stage development will have been concluded before the upper thermal tolerance limit of the upper sixties to lowe r seven tie s is a t t a ined . En t ra inmen t Effects: Negligible. Basis for Prediction: Applicant commissioned Stone and Webster Engineering Corporation to develop a sophisticated mathematical model to predict the ef fects of en trainment on this species. Using very ~ conservative assumptions the model predicts the loss to the mackerel population of 0 9 to 3.4%. This range represents 6. 7 to 20. 7% of the natural population G. 6-13
_ _ _ _ . .- . --. . ~ -- -. . . - . . -- - .- - NEP 1&2 1 oscillations predicted by inclusion of the respective input parameters.-
- Ihe small predicted impac t , magnified by the model conservatism, should not disrupt the normal pattern of the population.
- 6.1.11 Butterfish (Peprilus triacanthus)
Entrapment Effects: Minimal. I Basis for Prediction: Results from the comparative intake entrapment study indicated that this species has a medium to high entrapment potential. However, available data l on 'its abundance and distribution in the site area indicates that the location of the
~
proposed intake is not. a preferred habitat for butterfish. In addition, the swimming I capability of this species is sufficient to permit the. fish to avoid the intakes. Also, l this species will only be available in the area (and thus subject to potential 1 i en tragsment) from May through October. Fu r th e rmo r e , this species has a history of
'{
sporadic population peaks dnd' declines. Thus, in some' years few will oe available for entrapment. Consequently, the potential for significant entrapment impacts is judged minimal . l Thermal Effects: Min imal . 4 Basis for Prediction: The basis for such a prediction is derived f rom existing thermal l- ! tolerance literature, the organism's life history characteristics and known operating parameters. i ' As demonstrated by the literature, it is reasonable to assume butterfish are tolerant or even prefer. relatively warm water temperatures. The information presented suggests , butterfish eggs and larvae will not be adversely af fected by an induced tempe rature increase of 60F above ambient. The adults are not likely to be af fected by the plume e since they can freely avoid a stressful situation should it arise. 1 G.6-14 l
NEP L&2 [ Entrainment Effects: Neglig ib le. Basis for Prediction: Based on the plant operating at full load, 2.832 x 107 eggs and 6.621 x 106 larvee would have been entrained in 1974, and 8.889 x 107 eggs and 1.876 x 107 larvae, in 1975. Several aspects of the life history of this species are poorly documented. However, using conservative assumptions, Applicant estimated the loss during 1974 and 1975 due to entratament would have been 29,000 and 86,700 adults, respectively. This equates to approx'imately 7250 and 21,680 pounds of butterfish for the same years,
~
respectively. Since the 1971,1973 and 1975 average commercial landings in Rhode Island was 1,433,000 pounds, the loss due to entrainment of eggs and larvae 1974 and 1975 is, therefore, equivalent to 065% and 1.5% of the average commercial butterfish landing. 6.1.12 Winter Flounder (Pseudopleuronectes americanus) ( Entrapment Ef fects: Negligible. Basis for Prediction: The comparative entrapment evaluation, as well as available data on abundance and distribution in the area, identified several f actors which indicated that entrapment of winter flounder should not be substantial. The winter flounder, because ,of its af finity for the bottom and the design of the intake with the protruding lip, is not expected to be vulnerable to entrapment. Additionally, exper ience wi th its west coast ecological counterpart, the diamond turbot, has shown that even archaic velocity cap designs are ef fective in ' preventing entrapment of benthic flatfish. Furthermore, vinter' flounder are in relatively low abundance in the region of the pecposed intake, and also have a suf ficient swim speed capability to permit them to ' cvoid 'the in take structure. ' thermal Ef fects: Minimal Be-is for Predic tion: . The evaluation of the winter flounder thermal tolerance is based G. 6-15
NEP 162 on the Applicant's thermal assessment model. Such an analysts indicates a 60F Induced temperature rise talls well within the thermal tolerance capabilities of this species. Such a position is based on several f actors:
- a. The eggs of this species are demersal and adhesive, with the majority of spawning taking place in coastal salt ponds such as Ninig ret Pond. Th e r e f o r e , the probability of this life history stage being involved with the thermal discharge or being af fected by a design surf ace maximum within the boundary of the mixing zone is relatively small.
- b. The literature demonstrates rather conclusively that the juveniles can tolerate water temperatures well in excess of those anticipated once the plant is operational. Temperature tolerance limits for periods een juveniles are known to occur at' the site (i.e., winter and spring) exceed the proj ected surf ace maximum-(
temperature by anydiere from 3 to 180F.
- c. . As presented in Figure G.4.2-48, adult flounder are foend throughout most of the year at the proposed site. Of particular relevance is that a majotity of the temperatures of the temperature tolerance studies conducted coincide quite closely with the warmest wa ter temperatures that the adult would experience during the month of August. In all instances, the upper thermal tolerance limits exceed the anticipated surface maximum of 760 F that would be experienced within the boundary of the mixing zone. Irupacts as a result of thermal stress are, the ref o re , not anticipated.
En trainmen t Effect: Negligib le. Basis for Prediction: Winter flounder eggs are demersal adhesive and are, therefore, not subject to entrainment. G. 6-16
I NEP 1&2 ( The larvae of winter flounder, which are subject to entrainment, are concentrated inside Ninig re t Pond in densities which greatly exceed those found in Block Island Sound. A mathematical model, developed by Stone and Webster Engineering Corporation, estimated that only 1 5% of the Ibal's larvae will be entrained in the. unlikely event that a series of very conservative asstsaptions proved correct. Applicant estimated that during.1975 the plant would have entrained 4 577 x 108 winter 4 flounder larvae had it been operating at full load . This would "have resulted in the loss of approximately 20,070 pounds of spawning females or the loss of 14,164 pounds of three year old (breeding age) adults. Thus, the adults whose spawn la lost and the projected loss of three year olds represents 0 5% and 0.35%, respectively of the average 1971 through 1975 Rhode Island winter flounder landings. ( G. 6-17
l ~NEP 1&2 4 i i 1 i . ! 6.1.13 Blue Mussel (Mytilus edulis) Entrapment Effects: None _, 1 i f Basis for Prediction: With the exception of those mussels which are killed or which release their bysalt threads during backflushing operations, no mussels will be entrapped since they are a non-motile benthic invertebrate. Thermal Ef fects: Some thermal ef fect possible.- i i Basis for Prediction: The thermal assessment model generated for the blue mussel formed l the basis of thermal impact assessment for this mollusk. Such an evaluation indicates that the somewhat sensitive egg and larval stages could i be af fected to a limited degree. The overall potential for thermal ef fect is expected j ) to be small, however, based on several factors: first, to a great degree blue mussel i spawning activity and larval metamorphosts takes place before maximum induced surf ace water temperatures would approach temperatures which were, cited in the literature as I being limiting (i.e., upper seventies); second, the Applicant's mixing zone is small + l relative to the total area of Block Island Sound; and third, the species is noted for t being a prolific spawner. i
- Since adults are primarily associated with the bottom, any interaction with the thermal 1
] discharge plume is expected to be minimal for two reasons: (1) the expected peak ! l isotheras should not exceed the species' thermal tolerance limit, and (2) within the l confines of the proposed discharge area where the thermal plume could contact the botton
- there is a limited amount of suitable substrate (i.e., rocks) for mussel attachment.
G.6-18 _ . - _ - _ , , _ _ _ _ _ _ _ _ _ _ . _ . _ _ _ _ _ _ _ _ _ _ . _ _ _ . _ . . _ _ . _ _ . . _ _ . ~ _ _ _ . _ _ ,_ _- !
NEP 1&2 Entrainment Ef fects: Negligible. 1 Es-is for Prediction: Applicant estimated that 6.393 x 108 and 2 799 x 108 adult mussels would have been lost during the sampling periods 1974-1975 and 1975-1976, r espec t ively . Since the estimated losses for blue mussel at Pilgrim Station Units 1 and 2 are 3 8 to 8.2 times greater than those predicted for NEP 1 and 2, and since m'ussel larval entrainment losses of this magnitude luve been previously shown to have negligibic impact on adult mussel populations, it is concluded that mussel larval entrainment at NEP 1 cnd 2 should also be negligible. 6 1 14 Hard Clam (Mercenaria mercenaria) Entrapment Ef fects: No impact. Ba-is for Prediction: As 'a non-notile benthic bivalve, the hard clam will not be subject - ( ts entrapment. s Th rmal Effects: Negligible. Baris for Prediction: The basis for such a prediction is derived f rom a knowledge of j tha hard . clam's life history and thermal tolerance characteristics. I I Because of the known. ability of egg and larval stages to tolerate water temperatures in excess of 80 F, and the comparatively low densities of larvae observed in Block Island Sound, little, if any, thermal impact. is expected. In addition, no thermal impact is c::ticipated for the adult since & mercenaria beds are found almost exclusively in Minigret Ibnd and it'has been demonstrated that there will be no significant temperature rise in the Ibnd attributable to operation of NEP 1&2. Bitrainment Ef fects: Negligible. ) G. 6-19
NEP 162 Basis for Prediction: During the 1975 sampling year, a conservative maximum , density
~
of 1452/m3 hard clam larvae were observed in Block Island Saund. 1.arval concentrations of 7,500 to 10,000 per cubic meter have been reported by others. Applicant obse rved densities 'of Mercenaria in excess of 16,000 per cubic meter in Ninigret Po nd . Because the camparatively low density.of' hard clam larvae in Block Island Sound, it is predicted that negligible effects will occur due to the plant's operation. 6.1 15 Lotu-Finned Squid (Loligo pealet) Entrapment Ef fects: Negligibic. Basis for Prediction: Results from the comparative intake entrapment evaluation - indicates that this species will rarely be subject to entrapment. his assessment is stestantiated by experience at operating velocity cap intakes in Florida and California where both _ the long finned squid and its west coast counterpart, h opalesc en s , a re . I rarely impinged. Additionally, this species ha's an exceptional .swin speed capability which would easily permit it to avoid the in take s. Wernal Effects: Minimal. Basis for Prediction: The basis for minimal thermal impact to the squid was derived f rom integrating the species' life history and thermal tolerance characteristics with known plant thermal discharge operating parameters. he possibility exists that squid ' eggs, larvae and adults could be influenced by the Applicant's thermal discharge plume. Natural background water temperatures presented in the literature for egg laying, and development of eggs and larvae coincide rather closely with those induced wa ter temperature expec ted from plan t ope ration. Consequently, no appreciable tapact upon these early developmental stages is predicted. ( Similarly, thermal impact to the adult is also considered small due to the cephalopod's G. 6-2 0
NEP 1&2 1 l tobility and known zoogeographical range where natural background water temperatures I equal or exceed those expected f rom plant operation. l Entrainment Ef fects: Neg lig ib le. l _ Basis for Prediction: Squid eggs are laid in gelatinous strings on the ocean bottom and are not subject to entrainment. No intermediate planktonic larval form is produced and juvenile squid hatch directly frun the egg. Based on calculated average densities and assuming full plant load, Applicant estimated that 1.984 x 106 squid juveniles would have been entrained in 197 7. The proj ected entrainment of squid juveniles at hatching would thus result in the loss of 18,991 or 8,921 one year old squid, depending on the value of S used. ' These values equa te to o the loss of approximately.l.7 metric tons (3771 pounds) or 0.8 metric tons (1771 pounds). hose values equate to the loss of less than 0.008% of the minimum long finned-squid ( ctcck size which is recognized as stretching from Cape Hatteras to the northern edge f of Georges' Bank. Additionally, the projected entrainment loss is equal to less than 0.5% of recent Rhode Island landings. 6 1 16 Sand Shrimp (Crangon septemspinosa) Entracaent Ef fects: Negligible. 5seis for Prediction: Results from the comparative intake entrapment atudy indicated that this species has a low potential for entrapment. This assessac.nt la based on the factis that it prefers mobstructed sandy bottoms over the boulder atrewn area comprising the proposed intake location. Nethermore, sand shrimp tend to burrow beneath the sand and because of its benthic habits would generally not be available for entrapment. 4 hwraal Ef fects: Possibility of some thermal ef fect. C. 6-21
NEP 1&2 Basis for Prediction: The basis for such a prediction was dervied f rom the Applicant's
\.
analysis of the sand shrimp thermal assessment model. t Such an assessment indicates that during certain periods of the year (i.e., August) the induced bottom and surface temperatures (i.e., 6 F aba.e ambient) which the adult and larval sand shrimp could encounter approximate the upper temperature limits of this species. On the other hand, notably during the winter, early spring and f all, adult preference temperatures exceed any induced temperatures by as little as 10 F to as great as 250F. Even though the possibility of some plume interaction exists, any anticipated impac t is expected to be small for several reasons:
- 1. Since the female can move from an area should it prove un tenable and she retains the eggs in in her swimmeretts, nand shrimp eggs would not be entrained in the thermal plume.
- 2. The surface induced temperature plume approximates the upper thermal tolerance limit of the juvenile stage.
- 3. The expected induc ed temperature increase which the adult could experience on the bottom f alls within the upper thermal tolerance limit of this species. In addition, the adult is free to move from an area should it prove unsuitable.
Entrainment Effects: Negligible Ba sis for Prediction: An estimated 2.982 x 109 sand shrimp larvae would have been entrained f rom May 1978 to Kay 1979 assuming 100% plant load throughout the year. From entrainment estimates of equivalent Stage I larvae, an estimated 7.92 x 106 adult and i g shrimp would have been due to entrainment during 1978-1979. Based on estimated consumption rates of fish in Block Island Sound, the amount of adult sand shrimp lost G. 6-2 2
NEP 1&2 to entrainment was equated to 6.6 x 103 lbs. of fish or 0.0089% of Rhode Island's 1978 commercial landings. 6.1.17 American Lobster (Homarus americanus) Entrapment Ef fects: Neg ligib le. Baris for Prediction: The low entrapment potential of this species was based on data cn its abundance in the area, its biological characteristics, and its swim speed crpability. Results from field programs have shown that lobsters do not occur in unusually high numbers near the in take location. In addition, lobsters are benthic crganisms, being normally secretive in behavior, seeking shelter in burrows or beneath r:cks. Furthermore, available information on the swim speed capability of lobster indicates that this species could avoid the in take s. Tharsal Effects: Minimal. ( Basis for Prediction: Analysis of the Applicant's thermal assessment model forms the basis upon which this prediction is formulated. Results generated from the Applicant's model discussed previously in Section 4.2.16.3 indicates thermal impact to be small. Similar to the sand shrimp, the female retains ' the eggs in a brood pouch, and can move from the area should it prove untenable. Since lobster larvae are generally associated with the surface component of the plankton, there is a good possibility they will. be found in the surface discharge plume. However, tharsal tolerance data presented in the literature indicates a 6 F induced temperature rise falls ~within the reported tolerance range of lobster larvae. Any thermal' impact to the adult is also expected to be negligible due to the animal's mobility and demonstrated capacity to withstand reported test temperature as high as i 850F. C. 6-2 3
NEP 1&2 Entrainment Effects: Negligible. Basis for Prediction: Based on calculated average densities and assuming f ull plant load, 3.820 x 105 Stage I, 6.675 x 104 Stage II, 3 154 x 104 Stage III, and 1 450 x 104 Stage IV lobster larvae would have been entrained in 1977. Fo r 19 70, the projected entrainment was estimated, a f ter data refinement, to be 5.080 x 10 5 stage I, 2.296 x 105 stage 11, 1.653 x 105 stage Ill, and 3.480 x 105 stage IV. From these projections, it was conservatively estimated that 3. 749 x 107 and 2 967 x 106 equivalent stage 1 lobster would have been entrained in 1976 and 1977, respectively. When these . equivalent stage I larvae were equated to the number of adult lobster that would have been recruited to the commercial fishery approximately 5 years later, it was found that 7880 and 638 minimum legal size lobsters would have' been lost during 1976 and 1977, respectively. i This lost rec ru t.tmen t represents 6698 and 534 pounds or 0.20% and 0.02% of the 1976 and 1977 Rhode Island land ings , respectively. 6.1.18 Eelgrass (Zoste ra marina ) Entrapment: Not applicable. Risis for Prediction: Because this species is confined within Ninigret Pond and because its primary means of reproduction is vegetative, no part of its life cycle is subject to entrapment. Thermal Ef fects: Negligible. Basis for Prediction: The basis for such a prediction is derived f rom a knowledge of the species' life history characteristics and an understanding of the Applicant's discharge plume behavior. Of particular relevance to this species' relationship to the Applicant's thermal C. 6-2 4
NEP L&2 specific to an open coastal environment and how they may fluctuate spatially and tempo rally. With the biological characteristics of existing populations intimately associated with and acclimated to the exist ing physical envirotunen t , a detailed understanding and characterization of the physical envirotunent is vital in assessing environmental impacts because whatever changes that may occur in these factors as a result of construction and operation of NEP 1&2 may likewise cause associated chang e s in the biological community. Inf o rma tion of the existing physical environment is provided in Section 2.1 of this Appendix. e existing biological environment - this information describes tne various components of the biological community (e.g., plankton, benthos, and nekton) and how.they naturally vary temporally and spatially. We information forms the biological bases for selecting representative linpo rtant spec ies .which undergo deta iled impact appraisals. Data on the existing aquatic envirorunent is given in Section 2.2 of ( this Appendix. e desc riptions of the proposed in ta ke and discharge systems and their physical and chemical effects - this information desc ribes the design, materials, dimensions, and . operations of the proposed circulating cooling wa te r sys t em. Information provided includes cooling water flows , intale velocities, condenser temperature rise, discharge perfomance characteristics, physical bounds of' impact areas (e.g., thermal plume size), biofoulind control and other operational f actors. R ese data identify the interfaces between power plant and the physical / biological enviroivnent and thereby delineates the pattmys of potential environmental impacts. In f o rma t ion on the proposed cooling water system is given in Section 3.0 of this Appendix. The U.S. Environmental Protection Agency designated a list of 17 species as the Represen ta tive Impo r tan t Species for NEP 1&2. Wis list of designated RIS was then subjected to a rigorous impact assessment as described in Sections 4.1 and 4.2 of this G. 6-2 6
NEP 1&2 Operational velocity cap intakes in southern California and Florida were examined with respect to design criteria, operational conditions and the faunas exposed to them. The NEP 1&2 Representative lupo r tan t Species were paired with ecologically similar species occurring in Florida and/or southern California. The life histories of the paired species were examined in detail, and the entrapment records of the California and Florida equivalent species were studied. From this information, as well as site specific data on the temporal and spatial abundance and distribution of the RIS, estimates of the relative entrapment potential NEP ll? holds for the NEP 162 RIS were prepared. This technique provides the best means possible for predicting the potential entrapment of the RIS since it is based on actual operating experience of similar in take s . Results of these RIS entrapment appraisals provided evidence that some of the RIS are subject to potential entrapment and [ impinge. men t ; however, in no case does this impact cause appreciable harm to the populations of RIS. Alternative intake designs and locations we re also evalua ted (see Sec tion 5.0) to determine whether these alternatives would provide a net measurable environmental benefit, commensurate with their costs. From this analysis, it is shown that the alternative intake designs or locations do not provide substantially improved levels of envirorsnental protection conmensurate with their cost.Thus, Applicant has demonstrated that the location,' design, construction, and capacity of the proposed NEP 162 cooling water intake structure reflects the best technolody available for minimizing adverse environmental impact. To evaluate impacts of the NEP 1&2 thermal discharge, Applicant consolidated intormation on temporal abundance and distribution, thermal tolerance, range, response of kIS populations to natural and above ambient temperatures, and on the physical extent of G. 6-2 8
NEP 1&2 were constructed to extrapolate entrainment estimates to the projected loss to the adult ' populations or to the commercial harvest. By this approach, Applicant's entrainment estimates are used to predict the short term and long term impacts on the populations of RIS. Results of these entrainment analyses indicate that no population of R1S will i i be so severely impacted that they will suf fer appreciable harm. d-t Impacts other than those due to construction, entrapment, entrained and direct the rmal r { effects can also occur due to plant operation. These impacts include ef fects of chemical and bioci.de discharges and such indirect lethal and subiethal effects as cold shock, gas . bubble disease, skinny fish syndrome, and premature spawning. The potential for l these additional impacts to occur was evaluated by Applicant (see Section 4.3 of this Appendix),' and found to be of low magnitude. This c'onclusion is based on the fact that 1 4 1 these categories of impacts are more likely to occur at shoreline. surface discharges,
. particularly those that utilize long discharge canals that do not prevent passage of nekton Lato the canal. Once in the canal, nekton are continuously exposed to undiluted I
plant ef fluent and are thus subject to maximum potential ef fluent impact, be it cold i shock, gas bubble disease, or any of the other above cited potential ef fects. NEP 162 f will discharge thermal ef fluent to the receiving water via an of fshore, submerged, high h ! velocity dif fuser (see Section 3 0). This discharge design promotes very rapid mLxing - 1 . with ambient water, and thereby reduces the potential for development of large areas f of confined, elevated temperature water that can result in the types of impacts described i tbove. As a result, no appreciable harm to the Block Island Sound aquatic populationu ! is expected to occur as a result of these other potential ef fects. l In summary, Applicant has integrated physical, biological and plant engineering design cnd operational information in evaluating af fects of construction and operation of NEP l , e
- 1&2 on selected populations of RIS. A construction technique, i .e . , tunneling , wa s l
1 selected to minimize construction impacts both in Ninigret Pond and Block Island Sound. l 4 I G. 6-30 ; 1 i
.- . . -;.__. . =. - - .
HEP L&2 W 7.0 BIBLIOGRAPHY Abbott, R. T. 1963, American Seashells. D. Van Norstrand Company, Inc., Princeton, New Jersey.
?
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Davies, C.1969. Mussels as a world food source. Encyclopedia of Marine Re' sources. F.E. Fir th, ed . Van Nost rand-Re'inhold. Davis, H.C. 1960. Ef fects of turbidity-producing materials in . sea water on eggs' and larvae of the clam (Venus (Mercenaria) mercenaria)'. ' Bi ol . Bu 11. ' 118 (1) : 48-5 4. Davis, H.C. and.Calabrese. 1964. Combined ef fects of temperature and salinity on development of eggs and growth of larvae of M. mercenaria and C. virginia. Fishery Bull. 63(3): 643-655. i De Mont, J.D. and R.W. Miller. 1971. First reported incidence of gas bubble disease G.7-3
NEP L&2 McCarty and R. Kennedy (chairman) National Symposium on Es t ua r ine Pollut ion. ' Proc. Stanford University. Press, Stanf ord, California 152-187 Frame, D.W. 1973. Conversion ef ficiency and survival of young flounder (Pseudopleuronectes americanus) under experimental conditions. Trans. Amer. Fish. Soc. 3. Fr itz , R. I. 196 5. Autumn distribution of ground fish species in the Gulf of Maine and adjacent waters, 1955-56. Ser. Atlas. Mar. Environment. Amer. Geogr. Soc. Folio 10, 1-3. Ralton, T.W. ,1891. The comparative fecundity of sea fishes. 9th Rep. Fish. Bd. Scot.. Part III, Sci. Invest. 243-268. Gif t, J.J. and Jr. R. Westman. 1971. Responses of Some Estuarine Fishes to Increasing Thermal Gradients. Dept. Environ. Sci . Ru tgers Un iv . New Brun swic k , New Jersey.
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.macroinvertebrates for Public Service Elec tric knd Gas Company, New Je rsey.
Merriman, D. 1941. Studies on the Striped Bass (Roccus saxatilis) of the Atlantic Coast. U.S. Fish. Bull. 50(35):1-77. Mihursky, life. J. A. and J.S. Kennedy. 1967. Water temperature criteria to protect aquatic 20-32. E.L. Cooper, ed. Special Publication 4. Am. Fish. Soc. Trans. 96 (1) Supplement: G.7-9
NEP 1&2 i i Paskausky, D. and D. Mirphy,1976. " Seasonal Variation of Residual Drif t. in Long Island Sound." Estuarine and Coastal Mirine Science. 4:513-522. Pearce, J.B. (1969). 'Ihermal Addition and the Be n thos , Cape Cod Canal . Che sa pe ake Science. 10:227-233. Pearcy, W.C. 1962. Ecology o f an estuarine popula tion o f winter flounder 4 Pseudopleuronectes americanus (Walbaum) . Bu ll . Bingham Oc eanog r . Co llec t . , Ya le Un iv . 18 (1) , 78p. Perchon, R.D. 1968. The Biology of the Mollusc. Pergamon Press, London. Perkins, it . C . 1972. Development rates at various temperatures of embryos of the northern lobster, llomarus americanus (Milne-Edwards) Fishery Bulletin. 70(1). Perkins, H.C. , C. B. Kensier , and A. P. Stickney. (Undated). The ef fects of high water temperatures on the survival of larvae of the northern lobster Homarus americanus (Milne-Edwards) under certain ' experimen tal conditions. Unpublished and undated report. Na tio nal lia r ine Fisheries Serv. Biol. Lab. West Boo thb ay Ha r b o r , Maine. ! Perlmutter, A. 1947. The blackback flounder and its f tshery in New England and New York. Bull. of Bingham Oceano. Coll. 11(1):1-92. Phillips, R.C. 1974g. Transplantation of seagrasses, with special ' emphasis on eelgrass, Zostera marina. h Aquacut ture. 4:161-176. ( Prakash,.A. 1967. Growth and toxicity of a marine dinoflagell' ate Conyaulax tamarensis. J. Fish. Res. Bd. Can. 24:1589-1606. Pratt, David M. and D. A. Campbell. 1956. Environmental f actors af fecting growth in Venus mercenaria. Limnoi . and Oceanon r. 1(1) : 2-17. Price, K.A. 1961. On.the biology of the sand shr imp, Crangon septemspinosa (Say), in the Delaware Bay area. Risters Thesis, Un iv . De l . 5 5 p p . Price, K.S. 1962. Biology of the sand shrimp Cranno 3 septemspinosa in the shore zone of the Delaware Bay region. Ches. Sci .3(4): 245-2 55. Prosild, A.E. 1932. Occurrence of Zostera and Zannichellia in Arctic North American. i Rhodora 34:90-94. Ralph, R.M. and D. E. Hunely. 1952. The se ttling and growth of wharf-like fauna in Port Nicholson, WIllington New Zealand. Vic toria Univ. Coll. Zool. Publ. 19:1-22. i 4 Raney, E.C. 1952. The life history to the striped bass, Roccus saxatilus (Walbaum) . Bull. Bingham OceanoRr. Coll. 14(1):5-97. J Ra thj en , W.F. 1973. No r thwe st Atlantic squids. Hirine Fisheries Review. 35(12). Raytheon Co. 1975. Charlestown Hydrographic Study, April 19 74 to Ap r il 1975. Final Report, Prepared for Yankee Atomic Electric Company, Westboro, Mass. Raytheon Co. 1977. Distribution and abundance of lobster larvae in Block Island Sound - G. 7-11
NEP 162 Saila, S.B., T.T. Ib lga r , a nd B. A. Rogers. 1968. "Results ut Studies Related to Dreuged Sedimen t Dumping in Rhode Island Sound ." Annual Northeastern Regional Antipollution Conference, Proc. July 22-2 4, pp. 71-80. Sa ila , S.B., J.M. Flowers, J.T. Ilughes. 1969. Fecundity o f the Ame r ic an lobster, Homarus ame r ic anus . Trans. Amer. Fish. Soc. 98(3):537-539. Saila, S. B. a nd S. D. Pratt. 1973. Mid-Atlantic bight fisheries. In: Coastal of tshore environmental inv en to ry , Cape !!a t te ras to Nan tuc ke t Shoals. UR I Mir. Pub. Se r . No. 22 Marine Advisory Service, UR I, Kingston, R. I. Sandife r, P. A. 1973. Distribution and abundance of decapod crustacean tarvae in tue York River estuary and adjacent lower Chesapeake Bay , Vi rg in ia 1968-1969. Cn e sa pe ake Sci. 14(4):235-257.. Sandifer, P. A. 1975. The role of pelagic larvae in recruitment to populations of adult decapod crustaceans in the York, River estuary and. adjacent Lowe r Chesapeake bay, Virgin ia . Est. and Coastal Mar. Science. 3:269-279. Sauskan, V. I. and V. P. Sereb ryakov . 1968. Reproduc tion and development of the silver hake (Merlucc ius b il inea r ls , Mitchilli). Problems of Ichthyology 6(1):398-413. Scarratt, D.J. 1964. Abundance and distribution of lobster larvae (llomarus aniericanus) in Northumberland Strait. J. Fish. Res. Bd. Can. 21:661-680. f Scarrett, D. 1973. Abundance, survival and vertical and diurnal distribution of lobster larvae in Northumberland Strait 1962-63, and their relationships with commercial stocks J. Fish. Res. Board Canada. 30:1819-1824. Schaefer, R . II . 1967. Species composition, size and seasonal abundance of rishes in the surf zone of Long Island, N.Y. Fish and Came Journal. 14(1)l-46. Scott, J.S. 1968. Morphometrics, distribution, growth and maturity of of fshore sand lance (Ammodytes dubius) on the Nova Scotia banks. J. Fi sh . Re s . Bd . Ca n . 25(9):1775-1785. Scott, W.C.M. 1929. A note on the ef fect of temperature and salinity on the hatching on eggs of the winter flounder (Pseudopleuronectes americanus (Walbaum) . Cont r ib . Can. Biol . 4 (11) : 13 7-141. Serchuk, F.M. and C. F. Cole. 1974. Age and growth of the cunner, Tauto,tolabrus adspersus (Walgraun) (Pisc es : Lab ridae) in the Weweantic River estuary, Massachusetts. Chesapeake Sci. 15(4):205-213. Serchuk, F.M. and W.F. Ha thj en . 1974. Aspects of distribution and abundance of the long-finned squid , Lologic peale t , between Cape llat teran and Geo rges Bank. Ma r i n e Fisheries Review. 3 6(1) . Setchell, W.A. 1920. Geographical distribution of the marine spermatophytes. IWil. Torrey Bot. Club . 4 7: 563-5 79. Sette, I . E. 1943. Biology of the Atlantic mackerel (Scomber scombrus) of North Ainerica. Part 1: populations. Farly life hist 1ry, including growth, draf t, and mortality of eggs and larval Fi sh Wild li fe Serv. Fish Bull . 50:149-157. G.7-13
NEP 1&2 Boston, th asach use t t s. Stone and Webster. 1976. Biological Modeling of the Effect of Entrainmen t to Four Selected Fish Species at the NEP 1 and 2 Site. Charlestown. Rhode Island. Report submit ted to New I:ng l.md Power Company. Stone and Webster Engineer ing Corpd ra t ion, Boston, Massachusetts.
' Stringer, Louis D. L959. The population abundance and ef fect of sediment on the hard clam. Hurricane D.unage Control, Narragansett Bay and Vic in i ty . U.S. Dept. of the In te rio r, Fish and Wildlife Service, Bos ton, Ma ssach use t t s.
Summe rs , W.C. 1971. Age and growth of Loliito peali, a population study of t.he common Atlantic coast squid. Biol. Bull., 141:189-201. Summers, W.C. 1969. Winter population of Loligo pealet in the Mid-Atlantic Bight. Biol. Bull. 137.
. Tagatz , . Mar tine E. 1961 Tolerance of striped bass and American shad to changes of temperature and salinity. Spec. Sci. Rep., U.S. Fish Wild. Serv. - Fish 388.
Talbot, G.B. 1964. Estuarine requirements and limiting f actors of striped bass. In: A,symposiun on estuarine fisherie_s. Trans. Am. Fish. Soc: Special Publication No. 1., 1966:37-49. , Templeman, W. 1934. Kating in the Ameican lobster. Contrib. Canada Biol. Fish. 8. [ Templeman, W.' 1937. Habits .and distribution of larvat lo'b s te rs , Homarus americanus. J. Biol. Board Canada, 3:345-347.- Templenan, W. and S.N. Tibbo. 1945. . Lobster invest igations .in Newfoundland 1938-1941. Newfoundland Dep. Nat. Resour. Res. Bull . (Fish) 16. Terpin, K.M., M.C. Wyllie and E.R. liolmstrom. 1977. Temperature preference, avoidance, shock and swim speed studies with marine,and estuarine organisms f rom New Jersey. Fo r Pub lic Se r. Elec. and Gas. Co. I'ch thyo log ic al As soc ia t e s . Inc. Bull. No. 17. Tesmer, C. A. and A.C. Borad. 1964. 'Ihe larval development of Crangon septemspina (Say) .
'1he Ohio Journal of Science 64(4):239-250.
Th omps o n , K.S., W.H. Weed 11I, and A.G. Taruskt. 1971. Salt water fishes of Co nnec ticu t . Connecticut State Cological and Na tural History Survey. Bull. 105. Tibbetts, A.M. 1975. Squid fisheries (Lolino pealet and Illex illecebrosus) of f the Northeastern coast of the United -States of America, 1963-74. International Comm. for the Northwest Atlantic Fishereis: 85-109 Turner, H.J. 1953. A review of .the biology of sorse cosamercial reollusks ut the cast coast of North America. Sixth Report on Investiga tions of the Shell-fisheries of Ma ssachuse t ts. Div . tu r. Fish. , De p t . o f Co nse rva t io n , Comia . o f Ma s s . , Bos ton: 39-74. U.S. Department of Commerce. 1974, 1975, 1976, 1977 and 1978. Rhode 191and landing , annual summary. NOAA/N' IFS. United States Environnental Protection Agency (USEPA). 1977. Authorization to discharge C. 7-15
. . . = . = . -. - ~ -. - , . - . . _ . . .. .
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- - Wr ig h t , E.G. 1965. - A coinparative study of . the 'ef fect of temperature on crustacean motor axons.. Proc. Exp. Biol. Med. 119:506-509.
Wyllie, M.C.S., E.R. Holmst roie, and R. K. Wa l lac e . 1976. Temperature preference, avoidance, chock, and swimspeed studies with marine and estuarine organ ts:ns trom New i Jersey. Ichtayological Assocla tes, Inc. Bulletin'No. I 5. Yankee Atomic Electric Company (YAEC) . 1979 NEP 1&2 Small Fish and Sand Shrimp Program. Third Quarter Prodress Report.
' Young, J.S. 1974. Menhaden and power plants - a growing concern. Ma r ine Fishe ries Review 36(10): 19-23.
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' b. TEMPERATURE TOLERANCE RANGE FOR JUVENILES WHEN TRANSFERRED FROM SALT WATER TO FRESH WATER 2a. SHOCK TEMPERATURE SURVIVED BY JUVENILES (MELDROM AND GIFT,1971)
- b. MAXIMUM AVOIDANCE TEMPERATURE
- c. WINTER MAXIMUM AVOIDANCE TEMPERATURE
- 3. SURVIVAL AND FEEDING INDICATED (DORFMAN AND WESTMAN,1970)
- 4. MAXIMUM TEMPERATURES FOR M.SAXA T/L/S IN NEW ENGLAND (MERRIMAN,1941)
- 5. UPPER AVOIDANCE BREAKDOWN TEMPERATURE (GIFT AND WESTMAN,1971)
. 6. TEMPORAL OCCURRENCE OF ADULTS IN NEW ENGLAND (BIGELOW AND SCHROEDER,1553)
NEW ENGL'AND POWER COMPANY NEP1&2 # ' ^'^ ^ AND TilERM A L CIIARACTERISTICS Environmental Report FIG UR E.G A.218 NEP1&2
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- b. AVOIDANCE TEMPERATURE RESPONSE da. MEAN A/OIDANCE TEMPERATURE FOR 7.9 CM (AVERAGE). IGIFT AND WESTMAN,1971)
- b. MEAN AVOIDANCE BREAKDOWN TEMPERATURE
- c. MEAN AVOIDANCE TEMPERATURE FOR 13,9 CM (AVERAGE)
- d. MEAN AVOIDANCE 8REAKDOWN TEMPERATURE Sa, TEMPERATURE WHERE SIGNIFICANT INCREASE OF SWIMMING SPEED OBSERVED (OLLA ET.AL.,19751
- b. MAXIMUM SWIMMING SPEED TEMPT:RATURE (JUVENILE)
- c. LOSS OF EQUILlBRIUM OBSERVED Ga. PREFERENCE TEMPERATURES FOR JUVENILES (WYLLIE,1976)
- b. AVOIDANCE RESPONSE TEMPERATURE FOR JUVENILES 7a. -PREFERENCE TEMPERATURES FOR JUVENILES (TERPIN, ET.AL.,1977) b.' AVOIDANCE TEMPERATURE FOR JUVENILES
- 8. AVOIDANCE RESPONSE TEMPERATURE FOR ADULTS (OLLA AND STUDHOME,1971)
NEW ENGLAND POWER COMPANY NEP1&2 RELATIVE TEMPORAL AI!UNDANCE Environmental Report AND TilEllM AL CII ARACTEltlSTICS FIG UR E G.4.219 NEP1&2
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- 2. UPPER LETHAL TEMPER ATURE (de SYLVA,1%9) 3a. SPAWNING RANGE (BIGELOW AND SCHROEDER,1953)
- b. HATCHING TEMPER ATURE NEW ENGLAND POWER COMPANY CUNNEll itELATIVE TEMPOltAI.
'- NEP1&2 AllUNDANCE AND TilEllMAI, CilAllACTEltlSTICS Environmental Report FIGt11tE G.4.2-30 NEP1&2 l
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N E P 10 2 ER RI. vision 4 JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV OEC 95 , , , , , , , , , , , 95 90 - - 90 85 - - 85 80 - - 80 75 - - 75 4
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NEW ENGLAND POWER COMPANY DISTRIBUTION AND AVERAGE ls-1 NEP1&2 DENSITY OF BUTTERFISil LARVAE l Environmental Report FIGURE O.1.214 NEP1&2
N E P 1 & 2 LR Revision 4 JAN FEB MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC 200 , ,, 200 l I ,8 I I I I I I I .
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.......... 1976 NEW ENGLAND POWER COMPANY WINTER FLOUNDElt s NEP1&2 TEMPollAL AllUNDANCE AT I! LOCK ISLAND SOUND STATION A Environmental Report -
FIG Ult E G.4.2-45 NEP1&2
N E P 1 & 2 ER Revision 4
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N E P 1 & 2 ER Revision 4 I l JAN fed. MAR APR MAY JUN JUL AUG SEP OCT NOV DEC 95 , , , ,, , , , _, , , , 95 s 90 - - 90 e46 --2 85 - 85
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- 1. NO MORTALITY OF JUVENILES REPORTED FOR 1-HOUR TFST (HOFF AND WESTMAN,1966)
- 2. INCIPIENT LETHAL TEMPERATURE RANGE FOR ADULT (HUNTSMAN AND SPARKS,1924)
- 3. DISCRETE INCIPIENT LETHAL TEMPER ATURE (McCRAXEN,1%31 4a. TEMPERATURE AVOIDANCE RESPONSE INITIATED (GIFT AND WESTMAN,1971)
! b. AVOIDANCE BREAKDOWN BEHAVIOUR (SEE TEXT)
- c. UPPER THERMAL TOLERANCE LIMIT (SEE TEXTl
- 5. PREFERENCE TEMPERATURE (MELDRIM AND GIFT,1971)
- 6. GROWTH TEMPERATURE RANGE FOR 1-YE AR OLDS (FRAME,1973)
NEW ENGLAND POWER COMPANY WINTER FLOUNDER j NEP1&2 RELATIVE TEMPORAL ABUNDANCE i AND TIIERM AL Cll AR ACTERISTICS Environmenta! Heport FIGURE G.4,2 48 NEP1&2
N E P 1 & 2 ER Revision 4 JAN FEB MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC 10.000 10.000 g y y ; y LARVAE I 1,000 - l i
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- i.
I NEW ENGLAND POWER COMPANY llLUE M' SSEL NEP1&2 TEMPO' .AL AllVNDANCE AT Environmental Retxnt FIGUlf E G. l.2 19 NEP1&2
N E P 1 & 2 ER Revision 4 5 x J 2
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' DENSITY OF ill, TIE MUSSEL, l NEP 1& 2 I, AItV AE l' Ell m3
( Environmental Report FIGUltE G.4.2-50 N E P 1& 2
N E P 1 & 2 ER Revision 4l l w e, gSc )-
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SCALE IN MILES 90 60 30': If HL )CYlSLAND ))\ l DISTitilltJTION ANI) AVEllAGE NEW ENGLAND POWER COMPANY DENSITY OF lil,UE MllSSEI. NEP1&2 I,AltV AE Pelt in3 Environmental Report FIGtlitE G.1.2 51 NEP1&2
N E P 1 & 2 ER Revision 4 l%s JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC 95 ., , , , , , , , , ,, , 95 90 - se - - 90 e se 85 - - 85 80 - I*' - 80 6
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; r i ":> (. Q , s .
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JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC
- 1. MINIMAL SPAWNING TEMPERATURE (ENGLE AND LOOSANOFF,1944)
, 2. OPTIMAL TEMPERATURE RANGE FOR LARVAE SURVIVAL. AND GROWTH (LOUGH,1974) 3a. TEMPERATURE RANGE FOR LARVAE SURVIVAL (BRENKO AND CALABRESE,1969)
- b. ERRATIC SURVIVAL OF LARVAE OBSERVED
- c. TEMPERATURE AT WHICH MORTALITY OF LARVAE OBSERVED
- 4. TEMPERATURE RANGE FOR SETTLEMENT OF PEDIVELIGER LARVAE (ENGLE AND LOOSANOFF,1944)
- 5. IPITOLERANCE OF JUVENILE MUSSELS FOUND (GONZALEZ,1973)
- 6. TEMPERATURE LIMIT FOR SOUTHERN BOUNDARY (HUTCHINS,1947)
- 7. TEMPERATURE LIMIT FOR NATUR AL RANGE (READ AND CUMMINGS.1967)
Sa. UPPER TOLERANCE TEMPER ATURE FOR MYTILUS: 105.4*F (HENDERSON.19291
- b. 24-HR MEDIAN TEMPERATURE TOLERANCE
- 9. ADULTS SUSCEPTI8LE TO PREDATION (PE ARCE,1%9) toe. TEMPERATURE WHERE MORTALITY OF ADULTS REPORTED fGONZALEZ,19731
- b. TEMPER ATURE FOR CESSATION OF FEEDING
- 11. WATER FILTRATION CAPACITY AFFECTED (WIDDOWS,1973)
) NE'W ENGLAND POWER COMPANY ' NEP1&2 RM.ATIVE TEMI' ORAL ABUNDANCE AND Tl!ERM AL CilARACTERISTICS Environmental Report FIGURE G.4.2 52 N E P'1 & 2
N E P 1Q 2 ER Revision 4 JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV OEC
~
~
l l l l l l l l l l l "s .
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1.0 E I v g g W . W 0 .1 I I I I I "l I I I I I 0 .1 JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC NOTE: AVERAGE OF SURFAC,E, BOTTOM, DAY, AND NIGHT (1977) i NEW ENGLAND POWEH COMPANY SQUID .lUVENil E
'I'EMPORAI, AllUNDANCE AT
'. NEP1&2 Ill,0CK ISI,AND SOUND STATION Ell Il Environmental Heport FIGUllE G.l.2 53 NEP1&2
N E P.1 & 2 ER Revision 4
~~'
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%. NEW ENGLAND POWER COMPANY DISTitilllTflON AND AVEltAGE DENSITY NEP1&2 OF SQUID JUVENILES Environmental Report FIG Ult E G..t.2-5 i NEP1&2
N E P 1 & 2 ER Revision 4 CRANGON SEPTEMSPINOSA TOTAL g. xd a d-9 u-a i 9 2-a ! bo f_ a-l ul { 3 t O 3-9. e a k[\ 4 2 . . . . . . y=. e . + #. MAY JUN JUL AUG SEP OCT N0Y DEC JAN FEB MR ffR mi narr i NOTE: AVERAGE OF SURFACE, BOTTOM, DAY, AND NIGHT i NEW ENGLAND POWER COMPANY TEMPOltAI, AI!UNDANCE AT I (- . NEP1&2 IILOC'K ISI AND sol 1ND STATION Ell fl Environmental Report
; FIGuitE G.4.2- 55 NEP1&2
N E t' 1 & 2 ER 3evision 4 M m 3
,wniG gE r PONU p
d g >S' *t> .81 / 39 ef.h BL OCK ISGND sound 3 g$ 21 *]Q' - ( s so' so. ,60 7 N 3 ' NO. PE R M ! 0 75 1.5 M AY 11,1978- A PRIL 24,1979 ' 3.0 AVERAGE OF D AY, NIGH T , , SCALE IN MILES 6,0
~
./
12'40' I e % NEW ENGLAND POWER COMPANY 1)lSTitilll!!'lON ANI) AVElt.\GE DENSITY NEP1&2 of Sand Shrimp Larvae per H3 (Surface E nvironmen tal Repor FIGUllE G.4.2 56 N E P'l & 2
N E P 1 & 2 ER Revision 4 1 - 4 h o 30 % rpoND NINION 3 gt h t >5
' 3.96 30' N
BL OCK ISL AND SOUNO 4, g 9 41 20' - (
/ 50* so-
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$r NO PER M BLOCK ISLAND SOUND o5 1.5 M A Y ll,1978- A PRIL 24,1979 3.0 AVERAGE OF D AY, NIGH T a i I l 4.5 SC AL E IN MILE S 6.0 90-y 72*40' NEW ENGLAND POWEH COMPANY ' I)lSTitillUTION ANI) AVElt AGE DENSITY NEP1&2 o f <;.inti Shr imp l.a rv.ie per M1 (l'io t t on)
E nvironmen tal He port FIGUllE G.4.2 5 7 NFP1&2
1 N E P 1 & 2 ER Revision 4 JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC 95 , , , , , , , , , , , 9'2 90 - - 90 85 - - 85 6 s 80 . . . . , 80 t 8 1 38 + 7 -da
- i ,5 -
- ,5
; 70 - e -
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.e
'i n 5 . - -
-LARVAE' TEMPORAL
% .' ABUNDANCE NO EGGS - ,5 f I e i t I i i i I I I JAN FEB MAR APR MAY JUN JUL A' G SEP OCT NOV DEC
' 1. TEMPEHATUn[ nANGE WHEi4E SA' > SHitlMP H AVL DECN CAPIUFIED IPHICE,19629 i 2. OfSCRETE INCUHATION TCMPEF8 e UFl[ (G 7 D AYS) lPHICE,.19G11 i 34. . LAf4 VAL TEMPE H AIURE FI ANGC (SANDIF ER,1915)
- b. TEMPEHATUME ff ANGE W6t[ftE MOST A00NDANT 44 TEMPCH ATUFit FI ANGE FOH AOULIS filAEFN[n,19161
- b. T[MPER ATUFIE F4 ANGE WHEHE MOST AUUNDANT
- 5. MAXIMUM TEMPCHATUHC WHE Itt SAND SHHIMP WEllE FOUND tH Ati NE n,1969)
- 6. CHCAf tST MOftTALITY IN LOW OtSSOLVE D OMYCEN $TUDIES (HAf FNL ft,19105
! 7. TEMPtil ATUHF WH[ftt FtflituARY ACCLIMAf t0 SAND SHillMP OtID (VE f tN!![54G AND V E f t NHf' HG,1910) ,i
- 8. PFIErt nFtED TEMPEftATUHE f Oil AOULTS (MriDHtM. Ii AL.,1974)
- 9. TEMPORAL OCCUHHENCE OF JuvtNILES,ADUL TS, AND L AHVAl' i
i NEW ENGLAND POWEH COMPANY
'O' '
I* It!'t.ATIVE Tidil'Olt Al, AllUNDANCh. ANI) TilEIDI AI, Cil AIt ACTERISTICS Environmental Report flClif t f, G, l.2.$ g NEP1&2
l l N E P 1 & 2 ER Revision 4 I l JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC 1 0 , , , , , , , , , , , M.0
\
l s L - s
- 8 I 8 2 S l 10.0 -
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\
0 .1
' ' ' ' I ' ' ' ' ' ' '
O .1 JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC
------ 1976 (INCOMPLETE YE AR) 1977 l NOTE:
1977 AVERAGE OF STAGE I IV, OAY, SURFACE DURING 1977 ,
- 1976 AVERAGE OF STAGE I IV, SURFACE,80TTOM, DAY AND NIGHT AT STATION EB-B OURING 1976 l
1,()llS t Elt & NEW ENGLAND POWER COMPANY .g.g39g,()lt Al, AllVNI)ANCE IN NEP 1& 2 ggg,g 3(.K ISI.ANI) SOllNI) E nvironmentai llepset FIGI ?lt E G.1.2 -%' N E P 1& 2 l l-
N E P 1& 2 ER Revision 4 t ,.- & p 30' N n,wGM ' ' y
/
- 30*
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ur
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NO. PER 1000 m3 N i 0 \ s 0.5 BLOCK ISL AND SOUND , I MAY 3,1977 - AUGUST 2,1977 2 o 1 3 g - __ _ _ j scat r m wt ts w
/
12 40' - lilSTilllit ri'l()N ANI) AVElf AGI: NEW ENGLAND POWEH COMPANY l3p,Ngg7y ()l? lj)ns[ Elt l, Alt V Al; NEP1&2 g g[ :l(l> A('E) l t)77 E nvuonnwn tal Repor t
,_-_ ~ . _ - . _ _ . . _ . . _ . _ . _ . _ _ _ _ ., _ .___.__. . _ _ _ _ . . . _ - . - _ _ _ . _ . -_
N E P 1 & 2 ER Revision 4 [ [ 4 } p D 9 h _M
- O e
t < 30' N pgntG gt ET POND i et k* C g>S 1.04 Y
' 30' BLOCK ISLANb SOUND ~
I g 0.32 v go.
, 60' y NO. PER 1000 m3
[ . 0
, 0.5 BLOCK ISLAND SOUND MAY 3,1977 - AUGUST 2,1977
0 1 3 I I SCALE IN MILES 72*40' -
# N NEW ENGLAND POWEFI COMPANY I) STitilll1 TION ANI) AVEll AGE NEP1&2 I)ENSITY OF II)flSTEll I.AltVAE fil(YlTOM) 1977 Enwironmen tal Report FIGlJitE G. l.2 61 NEP1&2
N E P 10 2 ER R; vision 4 ( JAN FEB MAR APR M AY JUN JUL AUG SEP OCT NOV OEC 95 , , , , , , ,, , , , , 95
. se 90 - -
90 3 .4 85 - f 3'5 85
.3 i 80 - ***
l - 80 a, ., 15 - - 15 m '3
, . 70 - -
70 =m g . in g
>- .r g 65 - -
65 g e r 2 3 W 60 - - 60 W m . ia , 5 Y
$ $5 - -
$$ g 50 --
50
't 45 - -
45 40 - - 40
.$$ $ h,',N~ ,'Y$'$,hkh?hl[hh.,4kh,aj&.l
~
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RELATIVE d c.:} p, ,5 4 , * . fjTf4 065 f } gt7 lQ.,4 . , gg'- - TEMPORAL JAN FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC t a. COMMENCEMENT OF HATCHING AT MASSACHUSETTS STATE LOBSTER HATCHERY
- b. MOST INTENSIVE HATCHING
- 2. UPPER LIMIT DEVELOPMENT AND GROWTH TEMPERATURE FOR EMRRYOS AND POST. LARVAL STAGES (PERKINS,1972 HUGHES et, al.,19721
- 3. UPPER LETHAL TEMERATURES FOR ADULTS (McLEESE,19561 4a. NO LARVAL MORTALITY FOR SHORT EXPOSURE PERIOD (PERKINS,et, al. UNDATED)
- b. MINIMAL MORTALITY OBSERVED AT SIX HOUR EXPOSURE
- 54. LOOSTER LARVAk SURVlVAL (TL50) FOR 24 HOURS (ROSTON EDISON,19751
- b. LOnsTER LARVAE SURVIVAL (TL50) FOR 2 HOURS
- c. LORSTER LARVAE SURVIVAL (TL501 FOR I HOUR SUSPECTE D
'NUM BE R /1000 M' NEW ENGLAND POWER COMPANY AMElt!CAN I OllSTElt NEP1&2 ItEI.ATIVE TEMPoltAI, AllONDANCE Environmental Report # ' ^
FIGUltK G A.2-62 NEP1&2
, m
~
. t ~
33 Q 3 b MEP IL2 !4TAKE CE$1RM AND tnCAT104 DEC15104 mit!! Estaottsn Cooline Svstem Parametersi f 3. a.2.1 t* I I
~
Survev Site Characteristics & t'saoe Ecological (2.2 & Anoendts 4) Hvdrograohic (2.4) Aeological (2.5) Usage f2.1)
, E4Vta0%"EMTAL CCM5fDERATICNS Em41gEEtw. CCh5tCER4 Tim 5 i i 4 4 6 6 4 6 6 6 i art Resource Aestrette Derestl Effects Entrasment Estratament Construction fectechnical Cost Biofoulins wave Sedteent Construction 2-
- Utt11:ation: (Backflush) (5.1.4.2 & (5.1.4.3 & (4.1.1.2 & (Section 3.4 (10.2) 8 Cetris Protect. Accumula. (4.1) m coareccial & (5.1.4.1 & - Acceedia 4) Annencia 4) Anoendia 4) tef. 23 of Control ion tion g
$s '
necreational AenendiaC.1) l l l Section 2.4 ( 3. 4. 2. 5. 3.6. 19.21 1 (2.a.19.2) "
. 8 (2.1) I t t i 2.5) i I I ' i 28
- . PJ . Vi; Evaluation of Alterrate Intaaes m Cashore vs. Offshore 3 ff p: (10.2 & Annendia C) I D $ CHshore Intake l ., Envi ronmeettal Engineering l same as above esceot same as above I nest % tie Note: ** n W ers in earenteeses refer to acorneriste sections of DEP 142 Procesee Intese Location Environmental 8esort (3.4: 1.2: 10.2) k _ re.eesi at'e; ; =E ivurm i o r. o 3 e b
( TABLE G.2.2-1
SUMMARY
OF BLOCK ISLAND SOUND BIOLOGICAL SAMPLING PROGRAM BIS Monthly Taxa Stations (1) Depths Frecuency Replicates Collecting Equipment and Comments Phytoplankton 1974(2) A.8/C D(3) 3 2/1 1975 A,B/C,D'
~3
'l liter Van Dorn Sampler 3 2/1 __ 2
~
1 liter Van Dorn Sampler Zooplankton P 1974 A,B/C DI4) 3 2/1 3 1975 A,B/C,D 3 2/1 250 liters pumped through a No. 20 mesh net 2 250 liters pumped through a No. 30 mesh net Lobster Larvae
'1976 BIS-A, BIS-B Surface Weekly .
2 1m x 2m neuston' net with imm~ mesh. Pre-liminary survey, incomplete coverage of spawning season. Day and night surveys. 1977 EB-B,EB-C 2 Weekly 3 EB-D,EB-E Surface Weekly 2m x 2m x 8m long tucker net with 0.950=m 3 mesh; day and night EB-B+EB-E - All Weekly 1 Oblique tow with 2m x 2m x 8m long tucker net with 0.950=m mesh Squid Juveniles ' 1977 EB-B EB-C, 2 Weekly 3 EB-D.EB-E - 2m x 2m x 8m long tucker net with 0.950mm mesh. Surface and near-bottom towing; day and night i EB-B+EB-E -1 Weekly 1 Oblique tow with 2m x 2m x 8m long tucker net with 0.950mm mesh Send Shrimp 1978-1979 Larvae EB-B EB-C 2 Note (9) 3 EB-A.EE-D Surface 0.75m x 0.75m x 6m long tucker net with Note (9) 3 0.333mm mesh. Surface and near-bottom
. towing; day and night Adults EB-C Botton Note (9) 3
<~ 12 ft.
and semi-balloon night shrimp trawl.-~cDag' i r-
],,,, . .
A! .~ i
TABLE G.2.2-1 (Cont.)
SUMMARY
OF BLOCK ISLAND SOUND BIOLOGICAL SAMPLING PROGRAM BIS Monthly Taxa Stations II) Depths Frequency Replicates Collecting Equipment and Comments Ichthyoplankton 1974 A,B.C D(5) All Note (6) 3 Oblique Bongo (.333p and .505u mesh) tows f 1975 A+P All Note (6) 1 Oblique Bongo Benthos 1974 Note (7) - Quarterly 3 Divers troweled out an 0.5 x 0.5m square to a depth of 10 cm 1975 Note (7) 2 0.04 m2 Van Veen Sampler Finfish 1974 A,B,C Bottom Note (8) 2 38' otter trawl A 0-10' Note (8) 1 500' experimental gill net set on bottom 1975 A,C Bottom 2 2 Co=mercial Dragger (1) See Figure G.2.0-1. (2) 1974 represents April 1974 through March 1975; 1975 represents April 1975 through March 1976. (3) The "/" indicates two sampling strategies. Letters to the left and right of the "/" correspond to similarly located nu=bers in the monthly frequency column. (4) Night samples were also taken at A and B at roughly monthly intervals. (5) Duplicate, depth profiling .505 mesh tucker trawl collections were taken five times during the su=mer at stations A, B and C. (6) k'eekly April-August and then monthly (weekly during March 1976). (7) 3 parallel transects were sa= pled at 10' contour intervals to 80' (1974) and 10'-80' (1975). (8) Otter trawl - bimonthly April-August; Gill net - bimonthly Sept. and Oct.; Monthly thereafter. (9) Twice per month, day and night, from April through November, and once per month, at night, from December through March.
A ( \ Table G.2. 2 2 y
SUMMARY
OF NINIGRET POND BIOLOGICAL SAMPLING PROGRAM : A Monthly Taxa StationsII) Depths Frequency Replica *es Collecting Equipment and Comments Phytoplankton 1974(2) A,B,C,D,E/F(3) 2 2/1 3 1 liter Van Dorn Sampler 1975 A,B,C,D/E,F 2 2/1 2 1 liter Van Dorn Sampler Zooplankton 1974 A,B,C,D E/F 2 2/1 3 250 liters pumped through a No. 20 mesh net 1975 A,B C.D.E.F 2 Note (6) 2 250 liters pumped through a No. 30 mesh net Ichthyoplankton 1974 A,B,C,D E all Note (4) 2 oblique Tucker (.333u mesh) tow 2 1975 A,B,C,D E all Note (4) 2 oblique Tucker (.333s mesh) tow m o Benthos -. 1974 A,B,C,D,E - quarterly 3 Divers troweled out on 0.5 x 0.5m square to a [ depth of 10 cm m quarterly 3 0.04 m2 Van Veen Sampler 3 1975 A.B.C.D.E - Finfish 1974 A,B,C.D.E Bottom 2 2 19 foot ballon trawl Near A,B.C.D - Note (5) 1 60 foot beach seine 1975 As in 1974 except otter trawl frequency reduced as in note (5). 2 Bottom 8(7) 1 Commercial gill net (1) See Figure G.2.0-1. I2) 1974 represents April 1974 through March 1975;1975 represents April 1975 through March 1976. I3IThe "I'* indicates two sampling strategies. Letters to the left and right of the "/" correspond to similarly locsted numbers in the monthly frequency column. (4) Weekly April- August and then bimonthly (weekly in March 1976L ~ (5) Bimonthly Apnl- August and then monthly (bimonthly May - August in 1976)- (6) April 2, May 3; Jane and August 4; July 5; Sept - March 2.Jan O. U) September through March.
l N E P 10 2 ER lievision 4 Table G.2.2-3 (. ,, FINFISH $PEClES OBSERVED IN ICHTHYOPLANKTON COLLECTIONS Ninieret Fond Riock laland Sound l Common Name Scientific Name 1974 1975 1974 1975 American vel Angwlla rmtrata J' J J Conger vel Conger occamcus L Alewives Aloms sep- L L L Atlantic menhaden theroortw tyrannus Eil, Ell, E/L F,/L Atlantse herrmg Clupea harengus harengus L la L L Anchovies Anchar spp. L L L L Striped anchovy Anchoa tvi'<<tus E E Ilay ant hovy anchewr matc'hth E E E E Ramhow amelt Osmerus morda E EiL E Goowfash tophius ameruunns E E/L L E/L , Codfishes Gathdae E E i Cusk 11ronme brosme 1. Fourheard rockhng I:nchclyopus cim6nus E/L Elf, E/L E/L ' Atlant6c tod Gadus morhua E Elli I, E/L' liefdock Alelanogrammres argIcfmus I, L Silver hake (whiting) Af<rlucerus hshneris E E/L E/L E/L
- i. l' allot k Ibitachaus nicne I, I,
, Eil, llake ' f rroph yru .pp - E/ L Ell, E/L Cusk +els+el pouts Ophuhuf ar Zoariul.ie L L 1. L Atlantic needleftsh Strongslura marma I, E Kilhfishes fundulas .pp. E!!, E/L Mummichog Fundulun heterochtus J i
Silversules 3fenid44 .pp E/I, E/L L. Tidewater adversid, Aremd,a her3 thna Elf, Atlantic silversule Atenedia menhfur E { Stu hlehacks Ca tero tent.se Ell, E
. Fourspm, stii kichai k dpeltr< esuadras ss Ell, L *
! Threespme sticklehark { Gasterostas aculcatus L 1. L ! Sea horses //sppocampus sp t L L l Northern pqefish' Sygnathus fuscus J J J J ! lilack wa bass l'entroprutss streata I, I, I, j Scup Stenotomue chrysops E/L E/L j Wesh fish Cynoscson regahs E < !, L E/L E/L l Northem kingfish Alenteirrhus senatshs E Ell, E/L I, l Wrasace Lahridae E E E E l Tautog Tautoga onsten I, I, L L \ Cunner Tautogalabrus adspersus L I, L L l Radiated shanny f!Ituna suhht/arcata I, L L I, Rock gunnel l'huhe gunnellus I, I, la Sand launces Ammodvten sep L I, I, I, Naked sohy Gohnosome hosre I,IJ Seahnard gohy , tiobunsoma gunsburgs L I, la I, Atlantic msckerel Scomber arombrus Ell, Ell, Elf, Ell, Itutterrnh Iv redue tr#ncenthus Ell, L Ell, Ell, Hea tobins Prismotus spp E/l, E/l, Ell, Ell, See raven I/cmstreptenas americanus la Sculping Afvoronphalus spp 1, f, l, I, See snails Liparas app. 1, I, I, la Smallmouth flounder l'tropue morrootomus Ell, I, E/L Summer flounder (flukel Ibrahrhtlevs dentatus I, . I, I, Ell, Foutspot flounder Ibrahchthu oblimgus E/L . Ell, Ell, Wmdowpane
- Scophthalmus aquoeus E/I, E/l, E/1, E/l, Yellowtail flounder I.imanda /erruginea Ell, Elf, 10 / l, Ell, Witrh flound*r tilyptocephalus cynoglossus Elf, EIL American plahre floppogloesndes platessoideo I, L Wintor flmmder Pseudopleurrmectes amerscanue L Elf, I, E!!, '
llogchoker 7)inertes maculatus E/l, E/l, E/L E/L Northern puffer Sphoernedes maculatus 1, L 1, y
. J Juvenile, E = eggs, L = larvae
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( .- Table G.2. 2-6 y 3 MEAN CATCH (PER l00 M )OF SELECTED FISH EGGS l-TAKEN AT STATIONS BIS A THROUGH BIS D IN BLOCK ISLAND SOUND i CALCULATED FOR MONTHLY PERIODS l APRIL 1974 - MARCH 1976 (Sheet 1 of 2) Upper Value Represents 1974-75 Catch; Lower Value, 1975-76
% of Species Apr. May June July 'Aug. Sept. Oct. Nov. Dec. Jan. Feb. Mar. Total B. tyrannus 0 0.5 0.3 0 0 0 0.1 0 0 0 0 0 0 01 0 0.1 0.1 0 0 0 5.8 12.8 0 0 0 0 0.1 Anchoa mitchilli 0 0 12.1 1.3 0 0 0 0 0 0 0 0 0.2 0 0 5.4 26.1 0 0 0 0 0 0 0 0 0.6 Enchelyopus.Urophycis- 16.8* 16.5 35.0 8.0 1.3 1.0 0 0 0.04* 0.07* 1.1
- 14.2* 0.9 Peprilus 14.9 20.1 34.1 21.8 3.2 0.1 0 0' O.2
- 0.9
- 0.4
- 18.1* 1.6 Z
E cimbrius III - 7.0 5.4 1.6 0.4 0.1 0.2 0 0 0 0 0 0.2 m 12.5 5.8 0.6 0.1 0 0 0 'O O O O 0.8 'O G. morhua - - - - - - - - - - ge 0.2 0 0 0 0 0' G.6 9.3 11.6 3.1 5.0 0.2 m m P. virens - - - - - - - - - - - - - D 0 0 0 0 0 0 0 0 0 0 0.4 0.01 Gadidae or Gadid. 2.1 1.4 0.6 0.04 0 0 0.3 35.0 9.2 4.6 4.0 2.5 0.2 Glyptocephalus 1.6 0.4 0 0 0 0 0 6.6+ 9.3+ 11.6+ 3.1 + 5.4+ (0.3) Merluccius-Stenotomus- 0 10.1 16.8 6.0 0.1 0.7 0 0 0 0 0 0 0.4 Cynoscion 0 3.0 73.2 12.0 0.1 0 0 0 0 0 0 0 1.4 Urophycis spp. III O 0.4 10.1 4.0 0.2 0.1 0.07 0 0 0 0 0. 0.1 0 0 2.5 3.5 1.0 0 0.2 0 0 0 0 0 0.2 Labnd-Limanda 14.9 305.3 1774.9 774.2 15.1 0 0 0 0 0 0 1.4 " 34.5 4.4 240.4 1623.4 635.0 6.2 1.5 0 0 0 0 0 1.9 " 40.3
*All considered to be E. cambriss at this time. " All cortsuiered to be L ferruginea at this time. 'To permit compansons with 1974 - 1975 G. morhua and P. nrens have been added.
Table G.2. 2-6(cont.) 3 MEAN CATCH (PER 100 M )OF SELECTED FISH EGGS TAKEN AT STATIONS BIS A THROUGH BIS D IN BLOCK ISLAND SOUND
. CALCULATED FOR MONTHLY PERIODS, APRIL 1974 - MARCH 1976 (Sheet 2 of 2)
Upper Value Represents 1974-75 Catch, Lower Value, 1975-76
. % of Species Apr. May June July Aug. Sept. Oct. Nov. Dec. Jan. Feb. Mar. Total Labridae III O 136.6 827.7 142.0 5.8 3.1- 0 0 0 0 0 0 12.9 0.1 79.2 425.9 326.1 2.0 0.1 0 0 0 0 0 0 13.8 S. scombrus 6.3 3419.0 78.5 0.7 0 0 0 0 0 0 0 0 47.6 1.5 '2267/8 9.9 0.9 0 0 0 0 0 0 0 0 34.3 Prionotus spp. 0 2.7 29.3 26.8 8.9 2h 0.07 0 0 0 0 0 0.8 0 0.9 22.9 24.4 9.9 =.9 0 0 0 0 0 0 1.0 2
E. microstomus 0 0 0 0 0 0 0 0 0 0 0 0 0 m 0 0 4.7 13.2 11.9 3.8 0 0 0 0 0 0 0.5 m Pumlichthys- 1.8 46.8 56.0 12.3 1.1 58.6 3.5 0 0 0 0 0 1.6 y Scophthalmus 0.9 109.1 108.0 35.5 3.7 17.7 11.0 0 0 0 0 0 4.2 y m
- D Total eggs (total 41.9 3947.5 2888.2 979.6 33.2 66.4 2.1 35.1 9.2 4.7 5.1 18.1 -
includes all 26.4 2736.8 2338.7 1120.0 38.9 24.1 16.9 19.4 9.5 12.9 3.9 25.4 - species collected) s. 5'
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Table G.2. 2-7 (cont.) MEAN CATCH (PER 100 M3)OF SELECTED FlSH LARVAE TAKEN AT STATIONS BIS A THROUGH BIS D IN BLOCK ISLAND SOUND CALCULATED FOR MONTHLY PERIODS, APRIL 1974 - MARCH 1976 (Sheet 2 of 2) Upper Value Represents 1974-75 Catch, Lower Value 1975-76
% ot Species Apr. May June July Aug. Sept. Oct. Nov. Dec. Jan. Feb. Mar. Total ,tmmody'tes spp. 33.6 2.8 0 0 0 0 0 0 0.8 1.4 18.2 17.1 3.3 34.1 7.2 0.05 0 0 0 0 0 3.7 11.8 1.5 2.3 5.3 S. scombras O 85.1 275.1 3.3 0 0 0 0 0 0 0 0 33.1 0 98.3 364.0 2.8 0 0 0 0 0 0 0 0 21.3 Myoxocephalus spp. 4.9 1.2 0 0 0 0 0 0 0 0.1 1.7 3.6 0.6 4.3 1.0 0 0 0 0 0 0 0 0 0 3.9 0.8 Liparts spp. 4.4 9.7 0.5 0 0 0.06 0 0 0 0 0 1.2 1.4 2 3.4 7.2 1.1 0 0 0 0 0 0 0 0 0.5 0.9 m E. microstomus 0 0 0 0 0.02 0 0 0 0 0 0 0 0.01 O O O 1.5 18.3 6.6 0.3 0 0 0 0 0 1.0 y 0 N P. dentatus 0 0 0 0 0 0 0.4 0.2 0.1 0 0 0.01 0 0 0 0 0 0 0.8 0.7 0.4 0 0 0 0.02 $ . P. ob.'ongus 0 0 0.2 0.3 0.02 0.1 0 0 0 0 0 0 0.05 0 0 0 5.4 0.9 0.5 0 0 0 0 0 0 0.4 S aquosus 0 8.9 4.1 1.5 0.04 0.9 2.1 0.4 0 0 0 0 0.7 0 1.7 25.5 2.4 0.4 0.9 2.1 0.2 0 0 0 0 1.4 L ferruginea 1.0 20.0 4.0 0.2 0.04 0 0 0 0 0 0. 0 2.6 7.5 21.1 2.1 0.3 0 0 0 0 0 0 0 0 2.1 P. americanus 10.5 19.8 5.1 0 0 0 0 0 0 0.1 10.4 21.3 3.9 22.4 17.4 9.0 0 0 0 0 0 0 0 2.0 7.8 4.7 Total larvae (total 55.9 161.7 461.6 342.1 5.5 4.5 2.9 2.1 1.3 10.6 31 e 45.0 -
includes all species 74.5 177.8 864.6 608.8 122.0 15.1 6.2 12.9 7.0 21.2 47 15.5 - collected) m i-8-. a
- i
- ' Revision 4 N E P 1G 2 ER 4
- . i .
- m. Table G.2.2-8
,, PERCENT ABUNDANCE OF ICHTHYOPLANKTON l' Major Species Eggs Larvae Mackerel' 41% 27% i I, Cunner 37%* 26%
- I ,
Anchovy 0.4% 14% i Tautog 11%* 8% e i Winter Flounder - 4%
.! Sand Launce -
4% l Yellowtail Flounder 3%* 2% , I 92% 85% ., j 4
;
- Eggs not identifiable within these three; number represents
;/ v ratio of larval abundance times the percent of eggs for the
,4 - group.
, t 4
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N E P 10 2 ER Revision 4 Table G.2.3-1 l a FINFISH AND MACROINVERTEBRATES CAPTURED IN NINIGRET POND AND BLOCK ISLAND SOUND APRIL 1974 - MARCH 1976 (Sheet 1 of 2) Ninigret Pond Block Island Sound Common Name Scientific Name 1974 1975 1974 1975 Dusky shark Carcharhinus obscurus
- Smooth dogfish Afustelus canis *
- Spnny dogfish Squalus acanthias e Atlantic torpedo Torpedo nobiliana
- Bng skate Raja binoculata
- Little skate Raja crinacea * *
- Barndoor skate Raja laevis
- Winter skate Raja ocellata
- Amerncan eel Anguilla rostrata * * *
- Blueback herring Alosa oesticalis *
- Ilickory shad Alosa mediocris
- Alewife Alosa pseudoharengus * *
- American shad Alosa sapidissima * *
- Atlantic menhaden Brevoortia tymnnus *
- Atlantic herring Clupea harengus harengus * *
- Oyster toadiish Opsanus tau *
- Scup Stenotomus chrysops * * *
- Weaktish Cynoscion regalis * * *
( Northern kingfish bien ticirrhus saxatilis * *
^
Spot Leiostomus xanthurus
- J Spottin butterflyfish Chaetodon ocellatus
- Tautog Tautoga onitis * * *
- Cunner Tautogolabrus adspersus * * *
- White mullet Afugil curema
- Northern sennet Sphyraena borealis
- Atlantic bonito. Sarda sarda
- Atlantic mackerel Scomber scom brus *
- Chub mackerel Scomberjoyonicus *
- Butterfish Pepritus triacanthus * *
- Northern sea robin Prionotus carolinus * * *
- Striped sea robin Prionotus evolans *
- Searaven llemitripterus americanus *
- Grubby ofyoxocephalus aenaeus
- Longhorn sculpin ofyoxocephalus octodecemspinosus * * *
- Smallmouth flounder Etropus microstomus
- Summer flounder (fluke) Paralichthys dentatus * * *
- Fourspot flounder lkralichthys oblongus *
- Windowpane Scophthalmus aquosus * *
- Yellowtail flounder Limanda ferruginea *
- Winter flounder Pseudopleuronectes americanus * * *
- Ilogchoker Trinectes maculatus *
- Goosefish Lophius americanus *
- Atlantic cod Gadus morhua * *
- Iladdock hielanogrammus aeglefinis *
- Silver hake (waiting) Aferluccius bilinearis * *
- Attantic tomcod oficrogadus tomcod *
- v
R; vision 4 N E P.1 & 2 ER Table G.2.3-1 (cont.) FINFISH AND MACROINVERTEBRATES CAPTURED IN NINIGRET POND AND BLOCK ISLAND SOUND APRIL 1974 - M' ARCH 1976 (Sheet 2 of 2) Ninigret Pond Block Island Sound Common Name Scientific Name 1974'1975 1974 1975 Pollock Pollachius virens
- Red hake Urophycis chuss *
- Spotted hake Urophycis regis *
- White hake Urophycis tenuis *
- Ocean pout blacrozoarces americanus *
- Atlantic needlefish Strongylura marina * *
- Sheepshead minnow Cyprinodon turiegatus *
- Mummichog Fundulus heteroclitus *
- Striped killiiish Fundulus majalis *
- Silversides Afenidia spp.
- Tidewater silverside Afenidia berryllina *
- Atlantic silverside Afenidia menidia * *
- Foutspins stickleback Apeltes quadracus *
- Threespine stickleback Gasterosteus aculeatus *
- Bluespotted cornet fish Fistularia tabacaria
- Sea hor'se flippocampus erectus
- Northern pipefish Syngnathus fuscus *
- White perch Aforone americana *
( Striped bass Aforone saxatilis *
- Black sea bass ~ Centropristis striata * *
- Snowy grouper Epinephelus niveatus
- Bigeye iriaconthus arenatus
- Bluefish Pomatomus saltatr,ix * * *
- Crevalle jack Caranx hippos * *
- Atlantic moonfish Vomer setapinnis
- Banded rudderfish Seriola zonata
- Orange filefish Aluterus schoepfi * * *
- Planehead filefish 3fonacanthus hispidus *
- Northern putfer Sphaeroides maculatus
- Squid Loligo pealei *
- American lobster llamarus americanus * *
~.
N E P 1 & 2 ER Revision 4 Table G.2.3-2 ( CATCH OF TWO COMMERCIAL TRAWLERS JULY 1974 - MARCH 1976(3) Total Tows: 497 Total Pounds: 459,54G Species - Percent of Catch by Weight Silver IIake 29 Skate - 17 IIake and Ling - 12 IIerring 10 Flounder (2) 8 Squid 4 Sculpin 3 Scup 3 ( Ocean Pout 2 s Dogfish 2 Butterfish 1 Fluke 1 Cod 1 All Other 7 l i (1) I.ocation shown in Figure G.2.31. l (2) Primarily winter flounder and windowpane. i l r I J l-
~
( (~ Table G.2.3-3 PRINCIPLE NEKTON SPECIES TAKEN BY 45' STERN TRAWLER f E-AT TWO TRANSETSulAPRIL 1975 - MARCH 1976 i Species Inshore Offshore Combined % of Total Butterfish (2) 882 6428 7310 39.1 I Windowpane (2) 801 1199 2000 10.7 Scup 337 1581 1918 10.3 Little Skate (3) 422 1329 1751 9.4 Squid 617 1134 1751 9.4 2 Winter Flounder (3) 125 1393 1518 8.1 Ocean Pout (3) 106 429 535 2.9 N N Longhorn Sculpin(3) 16 394 410 2.2 g Red Hake 2 357 359 1.9 Silver Hake (3) 13- 330 342 1.8 Northern Sea Robin 160 127 287 1.5 Summer Flounder 76 66 142 0.8 All other 131 255 386 2.1
- 0) See Figure G.2.31.
(2) Analysis of vanance indicates that this species is more abundant offshore with 95% confidence. (3) Analysis of variance indicates that this species is more abundant offshore with 99% confidence.
!i)
- Table G.3.2-1
- l. Nearfield Thermal Plume Characteristics 3
; Current Surface Volume Within' Isotherm (Acre-ft)
Velocity ATmax . o (ft/sec) ( F) 30 F 20 F 10 F' 6F 3F 1 3.6 0.011 0.046 0.78 15 59 a 0.5 4.8 0.011 0.048 1.3 20 330
~
0.0 6.4 0.012 0.062 3.4 29 750 4 i i-l r! 4 f
- e -
f.g 4
. i.
5 ij-i ,e ' I ', f 3 i^
.I_
l' f
Table G3.2-2 Transient Plume Characterlattes CURRENT SPEED ISOTilERM* ('F) 30 20 10 4 3 2.5 I (FT/SEC) DILUTION 1.23 1.85 3.70 9.25' 12.3 14.8 Distance from 12 19 48 ---- 2400 6300-Discharge (ft) 1.0 Travel Time (sec) 0.65 1.1 5.5 ---- 2040 3960 Centerline' Velocity 18 12 4.6 ---- 1.15 1.09 Time = (ft/sec) T/4 Surface Area (acres) 0 0 0 0 16~ 71 Isotherm Volume 0.011 0.046 0.78 ---- 350 997 (acre /ft) Distance from 12 20 57 2010 3600 5700 Discharge (ft) 0.5 Travel Time (sec) 0.65 1.2 7.6 1330 3500 4700 Cente'line r V(locity 18 11 3.9 0.83 0.65 0.49 Time = (ft/sec) ST/12 Surface Area (acres) 0 0 0 7.1 33 76 , t Isotherm Volume 0.011 0.048 1.3 191 580 1800 (acre /ft) Distance from 12 21 78 2250 3200 6000 Discharge (f t) 0.0 Travel Time (sec) 0.66 1.3 14 1450 3470 7900 Centerline Velocity 18 11 2.8 1.5 0.97 0.12 Time = (ft/sec)
.T/2- .
Surface Area (acres) 0 0 0 12 33 131 Isotherm Volume 0.012 0.062 3.4 360 610 2270 (acre /ft) Distance from 12 20 57 1560 3400 4800 Discharge (ft) 0.5 Travel Time (sec) 0.65 1.2 7.6 1530 3300 6200 Centerline Velocity 18' 11 3.9 0.85- 0.64 0.63 Time = (ft/sec) 7T/12 Surface Area (acres) 0 0 0 5.0 32 64 Isotherm Volume 0.011 0.048 1.3 170 640 1150 (acre /f t)
N E P 1 & 2 ER Table G 3 4-1 CHEMICAL DISCHARGED DURING STEAM GENERATOR BLOWDOWN Normal Blowdown Discharge Maximum Blowdown Discharge (Eight Steam Generators at (One Steam Generator at Chemical 5 GPM Each)-LB/ Day 100 GPM) - LB/ Day Chloride 0.48 1.2 Fluoride 0.48 1.2 Ilydrazine 0.12 0.3 Silica ~ 0.48- ,- 1.2 Ammonia 0.24 L ^, [ Copper 0.024' O.06 .( Dissolved Iron 0.24 0.6 8
~
Lead 0.0024 0.006 e ' e 6
. G 9 e
em
-m +A
.m-
~- nW*'*
N E P 1 & 2 ER Revition. 4 Table c.4.1-1 . [ REPRESENTATIVE IMPORTANT SPECIES c Common Name_ Scientific Name Atlantic menhaden Brevoortia syrannus Bay anchovy Anchoa mitchilli Silver hake (whiting) Merluccius bilinearis Striped bass Morone saxatitis Bluefish - Pomato.nus saltatrix Scup Stenotomus chrysops Cunner Tautogolabrus adspersus Sand lance Ammodytes americanus Atlantic mackerel' Scomber'scombrus . Butterfish *Peprilus triacanthus _ Winter flounder : Pseudopleuronectes americanus
~ Mytilus edulis Blue mussel Mercenaria mercenaria ~
Hard clam Squid . Loligo pealei Sand shrimp . Crangon septimspinosus American lobster Homarus americanus Eelgrass Zostera marina l l f l l e a** **e* L1../I ,
N E P 1Q 2 ER Revision 4 L Table G.4.1-2 ENTRAINMENT OF EGGS AND LARVAE OF THE REPRESENTATIVE IMPORTANT SPECIES ASSUMING 100% POWER DURING
- STUDY PERIODU)
Species Year Eggs _ Larvae Atlantic Menhaden 1974 0 2.027 x10' 1975 8.592x10' 3.789x10' Average 4.296x10' 2.908 x 10 7 Bay Anchovy 1974 1.029x10' 5.243x10 8 1975 1.126 x10' 5.131x10' Average 6.147x10' 5.187x10' Silver llake 1974 3.054 x10' 8.614 x10' 1975 1.108x 10' 4.281 x 10' Average 7.069 x10 7 2.571 x10' Striped Bass - - - Bluefish - Scup 1974 2.946 x 10' 2.169 x 10' 1975 1.299x 10' 7.4 29x 10' Average 7.969x10 7 4.799 x 10' Cunner 1974 6.883 x10' 4.142 x10' 1975 6.202x10' . 7.471 x10' Average 6.543 x10' 5.806x10' Sand Lance
- 1974-1975 -
1.763 x10' 1975-1976 - 4.577x10' Average - 1.110x10' v Atlantic Mackerel 1974 3.558 x10' 2.038 x 10' 8, 1975 2.766 x10' 2.74 8 x10' Average 3.162x10' 2.393 x10' Butterfish 1974 2.832x 10' 6.621x10' 1975 8.889x10' 1.876x10' Average 5.861 x 10' 1.269x10' Winter Flounder 1975 - 4.577x10' 1976 - 2.221 x 10' Average - 3.399x 10' TOTAL ICHTIIYOPLANKTON Year 1 1.054x10 # 1.806x10' Year 2 9.419 x10' 1.874x10' Average 9.979 x10' 1.840x10' Mussel 1974 75 - 6.393 x 10' ' 1975-76 - 2.799 x10' ' Average - 4.597 x 10' ' flard Clam -
'4 (2)
Squid 1977 ,, 1.983 x 10' Sand Shrimp 1978-1979 - 1.982x109 American lobster 1976 (3) - 1.251x10* 1977 - 4.948x10 5 Average - 8.729 x 10' Eelgrasa -- - - I') plant Numbers flow based on area under temporal abundance curve at BIS-A or EB-B (Figure G.2.0-1) ti I'I Density is extremely low V (3) Estimate from an incomplete year and surface samples only (4) Revision 4 to Appendix G.
Revision 4 N E P 1 & 2 ER Table G.4.2-) ( LOBSTER LIFE TABLE STATISTICS UNEXPLOITED POPULATION Age Class Fecundity Per Adult (') Survival Rate (2 ) Relative Frequency 0 0 .00005951(3) 1,000,000 1 0 .86 59.51 2 0 .86 51.18 3 0 .86 44.01 4 0 .86 37.85 5 221 .86 32.55 6 1,679 .86 28.00 7 2,359 .86 24.08 8 3,129 .86 20.71 9 3,975 .86 17.81 10 4,890 .86 15.31 11 5,855 .86 12 13.17 6,865 .86-13 11.33 7,904 .86 9,74 14 8,939 .86 15 8.38 10,004 .86 7.20 16 11,052 .86 17 6.20 (. 12,086 .86 5.33 v 18 13,117 .86 19 4.SS 14,112 .86 20 3.94 15,108 0 3.39 (3 his column represents the first row of the Leslie matrix describing a stable population with a maxi-mum age of 20. 2 his column represents the subdiagonal of the above matrix. S = o k -
- as demonstrated by Vaughan and Saila (1976).
F1* i+1 j.g
'J
,- r- -
. . _ . - - - - . _ . _ . . _ ~ -. . _-
.. -, .-~
4 Table C.6.0-1 REPRESENTATIVE IMPORTANT SPECIES - IMPACT SQ?!ARY PLANT OPERATION Cooling Water Overall System Cumulative ___ Spe e l e s Ent ra pment Entrainment Thermal Construction Response 1 Atlantic menhaden Entrapment potentia.la No appreciable harm No appreciable effect Negligible impact No appreciable harm Med i u.n t o hi gh . Overall expected due to species' the rmal predicted predicted impact considered negligible tolerance capability j 1 Bay Anchovy Medium to high. Overall No appreciable harm Species very thermally No appreciable Overall impact
- impact considered small tolerant; c on se,ue nt ly , harn predicted considered minimal no impact expected.
Silver Hake Entrapment potential Minimal impact pre- Little or no effect No adverse effects No appreciable harm considered minimal dicted expected predicted predicted i i f Striped Bass Entrapment potential Not applicable Species very the rmally ' Negligible impact Minimal impact 4 _ considered negligible tolerant; therefore, predicted expected no impact predicted 3 a J Bluefish Minimal entrapnent Not applicable No impact expected due No construction No appreciable harm potential to species' thermal effects expected predicted tolerance Scup Overall entrapment No significant Negligible impact Minimal const ruct ion Minimal impact potential considered predicted inpacts expecteo expected J 1, pact ; I small Cunner Potential of localized 34 pop. reductions Minimal impact expected Possibility o'f Possibility of some impact; however, overall negligible impact temporarv disrup- localized impact or impact considered
- tm. ; however. displac ement minimal overall impact is small Sand Lance Low to medium entrapment Possibility of Possibilityofsomepiune Possible temporary Localized exclusion 4
potential. Total impact local entrainment contact, both t'mporally e effect on localized effect considered considered small effect .and spatially. Total egg densities. possible { impact considered ninimal Overall impact small
Table' G.* 6.0-1 (Continued) REPRESENTATIVE DiPORTANT SPECIES - IMPACT SLMtARY PLANT OPERATION Cooling Water Overall System Cumulative Species _ Entrapment Ent rainm.en t Therm al Construction Response Atlantic mackerel Entrapment not considered Entrainment not of Negligible thermal No appreciable a potential impact sufficient magnitude impact pr edicted Overall effects of construction effect plant operation to disrupt nor1nal predicted population considered small Eutterfish Medium to high entrapment Negligible entrainment tiinimal impact due.to Construction effects Cumulative impact potential; however, impact predicted due species' thermal considered tempor-considered not minimal impact expecte'd to relatively low tolerance ary resulting in no significant due to low numbers densities entrained appreciable impact Winter flounder Minimal entrapment potential As a result of low Negligible thermal due to species' bottom Tempora ry disruption Minimal effects re-densities entrainad, effects expected as a in area of construc- sulting from construc affinity minimal e f fects result of species' tion tion and cperation predicted thermal tolerance expected Blue mussel Not applicable Overall entrainment Some effect possible Possible temporary Possibility of some effects considered for a very small area. disruption, however, localized exclusion, slight Overall thermal effects recolonization should however, effects considered small.however occur considered negligible Hard clam Not ar licable Negligible e.ntrain- No thermal effect ex- Not applicable Cumulative impact ment effects due to pected due to species' considered minimal low plankton location in Ninigret Pond densitten Lcng-finned squid Negligible ef fects ex- No egg ent rainn.ent; No thermal effect. expected Possibility of some No appreciable impact' pected as a result of cor.r.equently mini- due to thermal tolerance disruption of demersal as a result of plant species' swimming ability mal entrainment im- of squid eggs; heweve r, only construction or pact expected temporary effect operation Sand shrimp Negligible effect due to Minimal entrainment Possibility of some bottom Temporary disruption Possibility of small organism's bottom af finity impact expected plu:ne contacts however, possible withi'n area area affected by area considered small of construction. thermal discharge. Overall effects con-sidered small
,- N
/. ~
Table C.6.0-1 (Continued) REPRESENTATIVE IMPORTANT SPECIES - UtPACT SLhMARY Pl. ANT OPERATION Cooling Water Overall _S >gi,e i s Entrapment Entrainment System Cumulative Thermal Construction ,
Response
Eelgrass Not applicable Not applicable Negligible Not applicable Cumulative effects predicted to be negligible American lobster Not applicable Miniraal impact Thermal impact considered Temporary exclusion; Overall construction resulting f rom minimal howeve r, cons t ruc- and operation effect' entrainment tion effect consider- considered minimal. ed small l
e, -g . APPLICATION FOR A DEPARTMtNT OF THE ARMY PERMIT For use of this form, sie IP 1145-2-1 The Department of the Army permit prograwn is authorized by Sectio-t 10 of the River and Hartwr Act of 1899. Section 404 of P. t. 92-500 and Section 103 of P. L. 92-532. These laws requite permits authorizing structures and work in or affecting navigable waters of the United States, the dischasge of dredged or fall materiit into waters of the United States, and the transportation of dredged the material application for afor the purpose of dumping it into ocean waters. Information provided in ENG Form 4345 will be used in e permit. Disclosure of the information regtsested is voluntary; however, the data requested are necessar applicant and to evaluate the permit application. cessed nor can a permit be issued. If necessary infe<mation is not provided, the permit applicatiori cieinot be pro-one set of onginal drawings or gaod reproducible copies which show the location and character of the proposed activity must be attached over to this the location application of the proposed(see sienple drawings and checklist) and be submitted to the District Engineer having jurisdiction activity. An apphcation that is not completed in full will be returned.
- 1. Apphcation number (To be assegned by Corps)
Revised 5/79
- 2. Date 3. For Corps use only.
26 April 1978 23-78-269 ,,, o,, y,,
- 4. Name and address of applicant.
- 5. Name, address and title r>f auttorized agent.
New England Power Company 20 Turnpike Road Joseph Harrington Westborough,i1A 01581 Project Manager - NEP~ 182 Telephone no, during business hours 20 Turnpike Rd., Nestborough, MA 01581 Telephone no. during business hours A/C (617i 366-9011 A/C 617 ) 366-43ll MC( ) NC( )
- 6. Describe in detait the proposed activity. its purpose and intended use (private. public, commercial or other) inciasding de tion of the type of structures, if any to be erected on tills, or pile or float-supported platt)rms, the type, composition geld quantity additionalofspace materials to be discharged is needed. use Block 14. or dumped and means of conveyance and the source of discharge or fill material.If
(- See attached information for: 6a. Offshore structures.in Block Island Sound (pages 3,4 & 5)- 6b. Barge unloading facility in Pt. Judith Pond (page 5)
- 6c. Site related work (page 6)
\
- 7. Names, addresses and telephone numbers of adjoining property owners lessees, etc.. mAose property also adjoens the waterway.
Item 6a. See sheet 1. Item 6b. See sheet 11 Dept. of Environmental Management Bruce C. Glen Item 6c. See Item 14 83 Park Street (pgs.667) & sheet 1 Post Road Providence, RI 02908 Charlestown, RI 02813 Sarah J. Browning (Does not adjoin waterway) U.S. Fish and Wildlife Service Post Road RFDl!1 Division of Refuges Bradford, RI 02808 1 Gateway Center Newton Corner. MA 02158
- 3. Location where proposed activity exists or will ocasr.
Address: 68., 6c. Naval Auxiliary Landing Field in Assessors
Description:
(if known) 6b.128 Pond Street Street, road or other descriptive location Map No. Subdiv. No. Lot No. 6a. and 6c. Charlestown; 6b. South Kingstown Ig or ng city' or town (Charlestown) 02813 Sec. Twp. age. and 6c Washington RI (So. Kingstown) 02881 , County State Zip Code .
, 9. Name of waterway at location of the activity.
6a. Block Island Sound 6b. Pt. Judith Pond ' 6c. Ninigret Pond ENG Form 4345.1 OCT 77 Edition of 1 Apr 74 ks obsolete.
to. D1ti nctivity ia proposco t3 coa.nence. 6a. Fall 1983; 6b. Fall 1981; 6c.1980 Date activity is e=pected to be compieted 6a. Fall 198S; 6b. Spring 1982; 6c.1982 E
- 11. Is any portion of the activity for which authorization is sought now complete? VES X NO Il answer is "Yes" give reasons in the remark section. Month and year the activity was completed
. Indicate the existing work on the drawings.
- 12. List all approvals or certifications required by other federal. interstate, state of local agencies for any structures. construc-tion, discharges deposits or other activities deteribed in this application.
Issuing Agency Type Approval Identification No. Date of Application Date of Approval See attached sheets (Pages 8 and 9)
- 13. Has any agency denied approval for the activity described herein or for any activity directly relate'd to the activity described herein?
Yes )( No (if **Yes" explain in remark?)
- 14. Remarks of additional information. Property owners, Item 6c, site related work.
See Sheet 1. L. V. Gaddes 151 Oak Lawn Avenue Cranston, RI 02920 ( Lawrence F. and Sarah A. Whittemore
.P.O. Box 245
'Charlestown, RI 02813 and 1161 Lairel Avenue Winnetka, IL 60093
- 15. Application is hereby made for a permit or permits to authoeiro the activities described herein. I certify that I am familiar with the information contained in this application, and that to the best of my knowledge and belief such information is true, complete. and accurate. I further certify that I possess the authority to undertake the proposed activities.
lhM$: (,$gnature'of Applicant or Authorize (Agent The application must be signed by the' applicant; however, it may be sigried by a duty authorized agent (named in item 5) if this form is accompanied by a statement by the applicant designating the agent and agreeing to fumish upon regaest, supplemental information in support of the application. 18 U. S. C. Section 1001 provides that: Whoever, in any manner within the jurisdiction of any department or agency of The United States knowingly and willfully falsifies concealm, or covers up by any trick, edieme or device a material fact or makes any false, fictitious or fraudulent statements or representations of enskes or uses any false writing or docasnent knowing same to contain any false fictitious or fraudslent statement or entry, shall be fined not more than $10.000 or imprisioned not more than five years, or both. Do riot send a permit processing fee with this application. The appropriate fee will be assessed when a permit is issued.
i. Item 6 6a. Offshore Structures in Block Island Sound New England Power Company has proposed constructing a two unit nuclear power station at the abandoned Naval Auxiliary Landing Field in Charlestown, Rhode Island (Sheets 7 and 8). The Offshore intakes and discharge dif fuser are to be constructed in Block Island Sound as part of a once-through cooling system to provide for heat removal f rom the main condensers and service water heat exchangers (Sheets 2 and 3). The intake system includes three identical offshore submerged intakes, one 18 foot inside diameter tunnel, an intake
^
transition structure and a pumphouse located on the site (Sheets 2 and 3). The discharge system includes a discharge transition structure, one 18 foot inside diameter tunnel, vertical riser shaf ts, and two 14 foot inside diameter discharge pipes with dif fuser nozzles attached. The 200,000 cubic yards of material f rom tunnel construction will be disposed.of at a suitable onshore location. The intake' structures will.be located approximately 2000 feet south of East Beach where the water depth is approximately 30 feet (Sheets 1 and 4). The velocity of the water at the inlets will be no greater-than 1.5 feet /second. The flow rate into each structure will be 285,000 gpm and is maintained during normal-operation throughout the year. The water from the three intake structures will combine and flow through the 18 foot inside diameter tunnel, approximately ( 6,200 feet in length, to the plant site. The discharge diffuser will receive the water, heated to a nominal 37 F above the-ambient, from the plant through the discharge. tunnel that will ext'end approximately 6,400 feet from the plant site. The discharge dif fuser will consist of two parallel 14 foot dif fuser pipes buried in an excavated trench with nozzles attached to the pipes and protruding above the ocean bottom. Vertical riser shaf ts will connect the diffuser pipes to the horizontal tunnel. One of ! the diffuser pipes will extend 600 feet seaward from the vertical l riser shaf ts; the other will extend 1,200 feet seaward. Each dif fuser will have 17 equally spaced two foot diameter nozzles, each having an exit velocity of 18 fps. The nozzles for the 600 foot diffuser will start at the vertical riser shafts and the' nozzles for the 1,200 foot diffuser will start 600 feet seaward of the riser shaf ts. Construction Techniques The construction of the tunnels through the rock will be accomplished by conventional methods (drilling and blasting) or by using a tunnel boring machine; both methods working f rom the plant site. Dewatering effluent from the tunneling operation will be' processed for. separation of any contaminants such as oils, diesel fuels, etc. The processed water will then be pumped to a settling basin as described in Applicant's application for a NPDES permit. Page 3
Offshore vertical shafts will connect the deep bedrock tunnels to the intake structures and discharge diffuser. These shafts may be constructed f rom a floating vessel commonly referred to as a jack-up barge. The jack-up barge will be positioned over the location of the shaft, and a steel casing then driven through the overburden deposits. Once the casing is firmly seated on bedrock, the overburden within the casing will be removed, and a large rock roller bit drill will be used to drill downward through the bedrock. A cylindrical steel shaft with a concrete lining will 2n be installed in the casing and anchored to the bedrock with concrete grout. The steel shaf t will contain diaphragm covers and valves to ensure that the ocean water does not enter the shaf t or tunnels until the appropriate time in the construction sequence. The completed steel shaf ts will support the three intake structures and also provide a transition
~
~
between the discharge tunnel and the pipe discharge diffuser. Material excavated from within the casings, estimated not to exceed 3000 cubic yards, will be deposited on the sea bed adjacent to the excavation. A typical intake structure is shown on Sheet 5. The intakes will be constructed'of reinforced, precast concrete or metal and barged or towed offshore for installation, or constructed in the dry utilizing steel cofferdams. Little, if any, environmental impact is associated with the operation. Sheet 6 is a schematic view of the multiport discharge diffuser through which the cooling water will be discharged. The diffuser k- pipes will be buried under the ocean bottom as shown, and will be installed subaqueously in an open cut excavation. Clamshell or bucket dredging will be used to remove the sediment from the diffuser pipe excavation. The total amount of sediment to be removed is approximately 122,000 cubic yards (includes 3000 cubic yards removed from the riser shafts), and will be placed alongside the trench. .The diffuser pipes will be supported by approximately 14,000 cubic yards of clean bedding material. It is anticipated that the excavated material will be suitable for use as backfill and subsequently up to approximately 94,600 cubic yards will be placed back in the trench after the diffuser pipes are installed in the trench. The excess material will be naturally distributed over the affected area such that the final bottom contours will not change significantly from original conditions. The final decision on the suitability of the material for backfilling will be determined from test borings, for which a Corps of Engineers permit has been received (Permit No. RI-QUOh-78-167) . If the excavated material is not suitable for use as backfill, it will be disposed of at an approved location. An alternate construction method will be considered should -the boring program determine that geological conditions are suitable. The bedrock tunnels would be extended the entire 1200 foot length of the diffuser. The diffuser nozzles would be installed ut'111 zing i a drilled-in concept, whereby diffuser nozzles are directly connected Page 4
to the bedrock tunnel via individual riser shafts of appropriate size. 6b. Barge Unloading Facility A barge unloading facility is required for the delivery of heavy and/or large equipment. The proposed location is the Stiver Spring Cove Marina in South Kingstown. After offloading, the equipment will ultimately be transported to the site, approximately 11 miles away, by road. The existing marina will be upgraded to service barges approximately 45 feet in width, 175 to 200 feet in length and requiring drafts up to 5 feet. Improvements include the installation.of a steel sheet piling bulkhead and wood piles according to the general arrangement shown in Sheet 10. Additionally, Applicant intends to dredge, and maintain while in use, the channel from the proposed bulkhead to buoy "C-25" as indicated in Sheet 9. Total material to_be dredged is approximately 17,000 cubic yards. Sedim~ent composition is described in the attachment. Sampling locations are depicted on Sheet 9. Sediments were collected from the top 6-12 inches with a gravity corer. Applicant plans to hydraulically ' dredge the channel f rom the buoy C-25 in front of the Ram Point Marina to the beginning of the barge slip area. The hydraulic ' dredge will pump the slurry to a holding basin for dewatering. Applicant will construct this holding basin in the { barge slip area by building a 1000 cubic yard earth dike (or sheet pile wall) out from the corner of the Silver Spring Cove Marina to the Route 1 roadway embankment. This dike will be constructed prior to beginning any dredge work. After the dredge. material'is. pumped to this holding area, the spoil material will be allowed to drain naturally or be mechanically dewatered in the basin. Once the material has been dewatered, it will be loaded onto trucks for transportation to an upland disposal area. The loading for transportation will be done by either a clam shell or front end loader since the holding basin would be dried out during the operation. This area would then be excavated down to the desired grade. If the existing bedding material in the barge slip area is not suitable for supporting the barge, then clean structural fill, not to exceed approximately 500 cu yds would be placed in that area. The sheet pile bulkhead will be constructed during the excavation of the holding basin. Once the holding basin area has been completed, the earth dike would be removed and construction in the tidal zone will be complete. During the construction period, it is anticipated that the marina boat haul will be temporarily relocated as shown
.on sheet.10.
Page 5
1 6c. Site Related Work' .i As part of the site erosion control program, a settling basin will be built to clarify site runoff. .The settling basin will discharge into a. percolation channel which leads to Ninigret Pond (Sheet 12). The channel will be formed by excavating a total of 4,400 cu yds and .then lining the -channel with 1,050 cu yds of 8 inch diameter riprap stone. Approximately 130 cu yds of the excavation and 100 ' cu yds of stone lining will lie below MHW. A riprap a' pron in Ninigret Pond will be laidf to prevent scour.- No excavation is proposed in the Pond below the normal high water mark. As shown in Sheet 13, no wetlands will be affected by this structure.
-Item 14 6a. Offshore Structures in Block Island Sound (Additional Information)
Submarine Cables i A submarine cable. area is approximately 2,000 yards west of the proposed offshore work area as shown in sheet 1 (reproduced from NOAA/NOS Chart 13215). A transatlantic cable comes ashore at Green Hill Point which is approximately 3 nautical miles to the east of the work area. Both.of these cable areas are distant enough from the work area that there is no possibility of damage to the cables. ( Ship Traffic There are no designated shipping channels or' lanes in Block Island Sound on NOAA/NOS Chart 13215. The chart does , indicate seaward limits for commerical fish traps which extend approximately 1,500 yards' from the coast.' Within this area large fish nets or traps (1/2. mile x 1/2 mile area) may be placed and attended to,. starting in late spring and continuing into the late fall. The proposed work site for~the'. offshore structures is within this fishing area. Block Island -- Sound is frequently used as a deep navigable waterway for ship traffic between Long Island Sound and Narragansett Bay and areas farther to the east, e.g., Buzzards Bay, Cape Cod, etc. These vessels do not pass close enough to' the offshore' construction site to constitute a hazard to the work platform or vessels servicing the work platform. The work platform will not be a hazard to
. commercial shipping, because shipping generally keeps about 4 miles off the East Beach coastline.
Small pleasure craft frequent the nearshore area but will be able
~
to avoid the work area since they rely on visual navigation when close to the coas.t. Proper navi,gational aids and warning lights - or bells will be installed and maintained at the work area as required by the U.S. Coast Guard. Page 6
p Ferry b' oat traffic in Block Island Sound . consists of ferry service from New London, Connecticut; Point Judith, Newport and Providence, Rhode Island; all to Block Island. The nearest of these ferry routes to the offshore work area-is approximately six miles, and therefore neither is considered a hazard to the other. i e 4 1 Page 7
Item'12 Date Of Date of IssuinR ARency Type Approval Identification No. Application Approval U.S. Nuclear Regulatory Class 103 Docket Nos.,STN Docketed Commission (utilization facility) 50-568 and STN 9/9/76 construction permit 50-569 and operating license Public Law 91-190,
. 83 Stat. 852 Rhode Island Coastal R.I. General Laws Resources Management Section 46-23-6 Council Permit and license for installation and main-tenance of circulating water system.
Approval of design, location and construc-tion of plant. Permit for ' dredging. U.S. Environmental Federal Water Pollution RI0020982 2/28/77 Protection Agency Control Act Amendments of 1972, Section 316 (a) and-(b)..Section 402. Alternate effluent limitation and NPDES discharge permits. Rhode Island Department Federal Water Pollution of Environmental Management Control Act Amendments of 1972, Section 401(a), and.R.I. General Laws Section 46-12-2(c), and 46-12-4. Circulating water discharge permit and certification to EPA and NRC. - '
, Page 8
S Date of Date of Issuing Anency Type Approval Identification No. Application Approval Rhode Island Department Construction on state of Transportation land. R.l. General Laws 24-8-4 Rhode' Island State R.I. General Laws Properties Committee Section 37-7-8. Ap proval of grant of interest in State property. Page 9
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$ee Sheef 9 for loi No. Referenees LOT NO. OWNER LOT NO. OWNER Wilson and f.dith Boothroyd Sandra Fish Cross
~oL I . 17 Arbor %y, Wakefield RIO2880 ; 3ia 17 Quagnut Drive,Wakefield , R.I. 02879 (NUons leased to N.E.RCo.)
311 & Christine, D. Bailetl Town of South Kingstourn 3to 186 Fairvieus Avenue,Walcott, Conn. Town Hall,66 High St. Wakefield,R.I. 02879 ota (Leased to Rom Roint Marina,Inc. 309 JosePh G.and Gilda A Sorag.ine clog. William Schmid.Jr. 40 Quagnut Drive., Wakefield,R.I.02879 i Salt Pbnd Road,Wakefield,R.I.02879) i 308 & Henry J. and Evelyn Prov'encher 318 A & Burton L. Little. 307 48 Quognut , Drive, Wakefield', R.I.02879 OL41A 83 Diane Drive,Vernon, Conn.06086 3os a Rene M.and MinnieJ.Bollen ier Sixty Six Acres Improvement Association 305 52 Quagnut Drive.,Wakefield, R.I 02879 3 87 % Mrs. William Nye.,Winchester Drive
%kefield, R.I. 02879 303 & Girl Scouts of America,Inc.
30+ % Council Officer 3 316 er
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313 - 314 Charles E. and Irene C.Redman State. of Rhode. Island 2 Newland Avenue, Uncoln, R.I. 02865 Department of Transportatiort State offs e Building Providence, R.I.' 02903 c/o Wendell rarley, Director et ste WAT nouir l
.TCTION C-C Foe LDCATION SEE SMEET 9
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- 20. 10 O 20 at the site Charlestown, Rhode Island SCALE IN FEET Application by New England Power N OT ES' Company PURPOSE: DISCH ARGE OF SETTLING BASIN EFFLUENT Sheet 12 of 13 Date: 4/17/79 D AT U M : MEAN LOW WATER MMW AND MLW MARKS ARE WITH RESPECT TO THE ATL ANTIC OCE AN. TIDAL R ANGE IN NiNIGRET POND IS 4-8 IN CHES.
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ATTACHMENT Barge Unloading Facility Sediment Composition 7 Application No. 23-78-269 May 1979 ( l i I i l l l l l I
f ~ o? Analysis Results from First Samples of Sedim'ent flat'erial (All results expressed as mg/g sludge except Coliforms as #/g) " 1 Coli fo rms" Kjeldahl Odor COD ' 011 & , Vol. Metals
. Total For:al N Inelex Croaso b
Solirin Pb Cu Zn Cr NL An Hg V Cd 1 200 0 1.6' l.5 .124 2.5 135 .22 .09. .37 .13 .04 .014 '<.001 .002 .03 2 2000 10 0.6 ~1.0 49 0.2 52 .05 .19 .06 .02
.09 .004 <.001 .001 02
'4.0 3 10000 2000 3.1 57 0.7 89 .14 .02 .003
.18 . 0'S . 06. <.001 <.001 .02 4 10 5.2. 81 90 100_ 2.0 1.7 .19 .09 .29 .09 .03 .005 <.001 .Ont .03
.5 2300 100 14.4 3.1 65 0.8 85 .24 .10 ' 31
. .11 .03 .012 <.001 .001 .03 6 100 10 2.8 3.1 '1'25 134 0.3 .08 .03 .09 .07 .03 .002 <.001 <.001 .03
'7 6000 600 7.0 4.9 . 114 <0.1 125 .31 .09 .27 .i6 .05 .015 <.001 .001 .03 lA 2.5 1.5 110' 2.8 166 .21 .06 .09
.23 .02 .014 <.001 .001 02 2A- 4'0. 1.0 82 0.2 70 .21 .08 .18 .08 .03 ,
.005 <.001 .001 02
'3 A 3.5 3.0 71 05 0.7 .24 .08 .20 .06 .02 .002' <.001' 001 0'2 4A 3.5 1.5 1.5 99 02 ~ .24 .11 .27 .08 .02 .006 <.001 .001 .0/
5A 2.0 3.1 80 109 0.7 .31 .16 .33 .14 .04 .011 <.001 .001 .04 6A 2.5 3.1 128 0.4 144 .05 .03 .07 .04 .02 .001 <.001 <.001 .03 7A 7.5 4.9 126 <0.1 133 .16 .09 .24 .13 .02 .011 <.001 .001 1 .03
.B.: "results expressed as mg NH4 C1/ g dry weight
! b results expressed as mg/g dry weight C
. " results expressed as mg/g wet weig'ht *
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