ML20079N002
| ML20079N002 | |
| Person / Time | |
|---|---|
| Site: | Pilgrim, 05000471 |
| Issue date: | 09/30/1977 |
| From: | BOSTON EDISON CO. |
| To: | |
| References | |
| RTR-NUREG-1437 AR, NUDOCS 9111110037 | |
| Download: ML20079N002 (150) | |
Text
{{#Wiki_filter:_ _ _ _ _ _ _ _ . ~ k [ [ ~ SUPPLEPINTAL ASSESSMENT IN SUPPORT CE THE 316 DEMONSTRATION PILGRIM NUCLEAR POh'ER STATION UNITS 1 AND 2 I BOSTON EDISON COMPANY I I I I SEPTEMBER 1977 P REPAPID BY E','?IPONMENTAL ENGINEEPING DIVISICN STC::E f, WEBSTEP ENGINEEFING CORPORATIO:; E 0 5 70:, , mas S A:_'h t. S t;TTS 9111110037 770930 PDR NURIIO 1437 C PDR
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'I r ! TABLE OF CONTENTS l Seetion Title Page ,, I. INTRODUCTION . . . . . . . . . . . . . . . . . . . . . 1-1 ! II . ASSESSMENT p (NOTE: The supplemental analyses described in this section q,~ are similar to those presented in Section 6 of the original 316 Demonstration of July 1975. Therefore, to facilitate , cross-ref erencing, the section and subsection numbers of this part of the report correspond to those used in the ,] original report. '~
- 6. IMPACT ASSESSMENT. . . . . . . . . . . . . . . . . . . 6.1-1 6.1 PROCEDURES FOR ASSESSMENT OF PILGRIM STATION'S
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EFFECT ON SELECTED SPECIES . . . . . . . . . . . . . 6.1-1 6.2 1RISH MOSS (Chondrus crispus) . . . . . . . . . . . . 6.2-1 6.2.1 Thermal Plume . . . . . . . . . . . . . . . . . . . 6.2-1 1 6.2.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.2-3 L 6.2.3 Entrapment. . . . . . . . . . . . . . . . . . . . . 6.2-3 6.2.4 Cumulative Impact . . . . . . . . . . . . . . . . . 6.2-3 3 k 6.3 6.3.1 ROCKWEED (Ascophv11um nodosum) , Ther:nal Plume
. . . . . . . . . . . 6.3-1
. . . . . . . . . . . . . . . . . . . 6.3-1 6.3.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.3-2 6.3.3 Entrapment. . . . . . . . . . . . . . . . . . . . . 6.3-2 6.3.4 Cumulative impact . . . . . . . . . . . . . . . . . 6.3-2 6.4 AMPHIPOD (Acanthohaustorius millsi) . . . . . . . . . 6.4-1
- 6.4.1 Thennal Plume . . . . . . . . . . . . . . . . . . . 6.4-1 6.4.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.4-1
; 6.4.3 Entrapment. . . . . . . . . . . . . . . . . . . . . 6.4-2 6.4.4 Cumulative Impact . . . . . . . . . . . . . . . . . 6.4-2
,^ 6.5 AMERICAN LOBSTER (Homarus americanus) . . . . . . . . 6.5-1 6.5.1 Thermal Plume . . . . . . . . . . . . . . . . . . . 6.5-1 6.5.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.5-1 6.5.3 Entrapment. . . . . . . . . . . . . . . . . . . . . 6.5-2 6.5.4 Cumulative Impact . . . . . . . . . . . . . . . . . 6.5-3 6.6 BLUE MUSSEL (Mytilus edulis) . . . . . . . . . . . . . 6.6-1 1- 6.6.1 Thermal Plume . . . . . . . . . . . . . . . . . . . 6.6-1
, 6.6.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.6-2 6.6.3 Entrapment. . . . . . . . . . . . . . . . . . . . . 6.6-2 6.6.4 Cumulative Impact . . . . . . . . . . . . . . . . . 6.6-2 i 6.7 COMMON PERIWINKLE (Littorina littorea) . . . . . . . . 6.7-1 6.7.1 Thermal Plume . . . . . . . . . . . . . . . . . . . b.7-1 I iii
I TA11LE OF CONTD4TS (CONT ' D) Section Title Page 6.7.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.7-1 6.7.3 Entrapment. . . . . . . . . . . . . . . . . . . . . 6.7-2 ~ 6.7.4 Cumulative Impact . . . . . . . . . . . . . . . . . 6.7-2 6.8 ATLANTIC MENHADEN (Brevoortia tyrannus) . . . . . . . 6.8-1 6.0.1 The Model . . . . . . . . . . . . . . . . . . . . . 6.8-1 6.8.2 Results of Thermal Plume, Entrainment, and Impingement. . . . . . . . . . . . . . . . . . . . 6.8-3 _ 6.8.3 Cumniative Impact . . . . . . . . . . . . . . . . . 6.8-4 6.9 WINTER FLOUNDER (Pseudopleuronectos americanus) . 6.9.1 The Model . . . . . . . . . . . . . . . . . . .. .
. . 6.9-1 6.9-2 I
6.9.2 Entrainment . . . . . . . . . . . . . . . . . . . . 6.9-3 E 6.9.3 Impingement . . . . . . . . . . . . . . . . . . . . 6.9-5 5 6.9.4 Thermal Plume . . . . . . . . . . . . . . . . . . . 6.9-6 6.9.5 Cumulative Impact . . . . . . . . . . . . . . . . . 6.9-6 3 gL 6.10 POLLOCK (Pollachius virens) . . . . . . . . . . . . . 6.10-1 6.10.1 Thermal Plume. . . . . . . . . . . . . . . . . . . 6.10-1
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6.10.2 Entrainment. . . . . . . . . . . . . . . . . . . . 6.10-1 6.10.3 Entrapment . . . . . . . . . . . . . . . . . . . 6.10-2
- 6. 10 .4 Cumulative Impact. . . . . . . . . . . . . . . . . 6.10-2 6.11 CUNNER (Tautogolabrus adspersus) . . . . . . . . . . . 6.11-1 6.11.1 Thermal Plume. . . . . . . . . . . . . . . . . . . 6.11-1 6.11.2 Entrainment. . . . . . . . . . . . . . . . . . . . 6.11-1 6.11.3 Entrapment . . . . . . . . . . . . . . . . . . . . 5' 6.11-3 5-6.11.4 Cumulative Impact. . . . . . . . . . . . . . . . . 6.11-3 m
6.12 RAINBOW SMELT (Osmerus mordax) . . . . . . . . . . . 6.12-1 g 6.12.1 The Model. . . . . . . . . . . . . . . . . . . . . 6.12-1 6.12.2 Cumulative Impact. . . . . . . . . . . . . . . . . 6.12-4 6.13 ATLANTIC SILVERSIDE (Menidia menidia) . . . . . . . . 6.13-1 6.13.1 Results of Thermal Plume, Entrainment, and Impingement . . . . . . . . . . . . . . . . . . . 6.13-1 g 4 6.13.2 Cumulative Impact. . . . . . . . . . . . . . . . . 6.13-2 g 6.14 ALEWIFE (Alosa pseudoharengus) . . . . . . . . . . . 6.14-1 6.14 .1 Results of Thermal Plume, Entrainment, and Impingement . . . . . . . . . . . . . . . . . . . 6.14-1 6.14.2 Cumulative Impact. . . . . . . . . . . . . . . . 6.14-2 6.15 REFERENCES . . . . . . . . . . . . . . . . . . . . . 6.15-1 III. CONCLUSION . . . . . . . . . . . . . . . . . . . . . III-1 iv a:
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TABLE OF CONTENTS (CONT ' D) Section Title Page
, IV . APPENDIC::S A. THERMAL 'IVLERANCE DATA A-1 I" B. LIST OF MARINE ECOIDGICAL AND HYDRAULIC STUDIES !. ASSOCIATED WITH PILGRIM STATION B-1 o
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LIST OF TABLES Table Descriotion 6-1 Irish Moss Harvest Statistics: 1971-1976 6-2 Parameters of Menhaden Population Simulation Model 6-3 Simulated Equilibrium of Menhaden Population ' 6-4 Predicted Numbers of Eggs and Larvae Entrained 6-5 Predicted Numbers of Fish Impinged 6-6 Results of Simulation of Menhaden Population 6-7 Parameters of toe Winter Flounder SLmulation Models 6-8 Results of Winter Flounder Simulation over a 40-Year Period 6-9 Summary of Entrainment Study, Pilgrim Station - Units 1 and 2 l 6-10 Species Composition of Gill Not Collections 6-11 Sport Fishing Catch at Pilgrim Station, 1973-1975 7 6- 12 Estimation of Age - Specific Fertility and Survival for Cunner 6-13 Life Table for Smelt 6-14 Initial and Equilibrium Population Structures for smelt S Lmulation E I f I I vi I
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! LIST OF FIGURES Fimire Title 6-1 Distribution of Chondrus crispus along the Plymouth Shoreline
.Lg 5 6-2 Comparison of Annual Irish Moss Harvest Statistics as j Related to Manomet Point 6-3 Comparison of Irish Moss Dry Weight Values 6-4 Potential Thermal Plume Effects, Irish Moss 6-5 Location of Five Transects for Benthic Sampling, 1971 to 1976 6-6 Mean Intertidal Density, Ascophv11um nodosum, in Dry
; Weight (G/M2) 6-7a Mean Density of Acanthchaustorius millsi at 20 feet ,, below MLW t
[ 6-7b Mean Density of Acanthohaustorius millsi at 30 feet below MLW 6-8 Lobster Pot Sampling Grid 6-9 Mean Lobster Catch per Pot 6-10 Potential Thermal Plume Effects, Lobster 6-11 Hean Intertidal Mytilu_s Density 6 12 Potential Thermal Plume Effects, Blue Mussel I 6-13 Density of Pvtilus (Bivalve) Larvae Observed at Unit 1, 1974 through 1976 6-14 Mean Intertidal Density of Littorina littorea 6-15 Density of Littorina (Gastropods) Larvae Observed at Unit 1, 1974 through 1976 l.1 6-16 The Ricker Stock and Recruitment Function 6-17 Menhaden Landings for All Massachusetts Ports 6-18 Depth-Averaged Particle Paths ; Velocities Taken f rom "Cafea Using Tide and 10-Knot Southwest Wind 6-19 Depth-Averaged Particle Paths; Velocities Taken from .
"Cafea using Tide and 20-Knot Northeast Wind vii I
I LIST OF FIGURrli (CONT'D) Fiqure Title 6-20 Location of Trawl Stations ' 6-21 Winter Flounder Trawl Catch 6-22 Numbers of Pollock and Cunner Collected in Gill Nets in Vicinity of Pilgrim Station i 6-23 Isocontours of Larval Depletion 6-24 Density of Menidia menidia Larvae observed at Unit 1, 1974 through 1976 E W 6-25 Density of Alosa pseudoharenqus Larvae observed at ' Unit 1, 1974 duough 1976 ' EI IL I!: E-I I-I- I. I viii Ir E
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. 1 I NTRODU C'I'10N This is a report on supplemental analyses which have been perf ormed in support of the "316 Demonstration for the Pilgrim 5 Nuclear Power Station Unita 1 and 2, Boston Edison company,"
which was published in July of 1975. Since the publication of the 316 Demonst. ration report, additional ecological and I hydrographic data have been collected at the Pilgrim site. These da ta are similar in nature to those used in the original 316 Demonstration report: therefore, although they u tiliz e an '3 o expanded data base by the inclusion of 1975 and 1976 ctudy 5 results, the present analyses are similar to the original .. analyses reported in July 1975. The analyses contained in this supplemental analysis are also similar to those applied in the 316 Demonstration in that conservative assumptions are used which result in overestimation I of the prediction or impact. Theretore, the predictions in this supplement should be viewed as upper bounds i". that the impact should be no greater than predicted and in many situations will ~;g probably be less than predicted. Some examples of the [E conservative assumptions are discussed below. I In estimating entrainment impact, it is assumed that 100 percent of the organisms die upon passage through the cooling system. Some information on mortality through the Pilgrim cooling system, which has a relatively brief transit time, supports the idea that some organisms survive passage. This mortality will depend upon species, lite stage and time of the year. Onsite atuales for gastropod and bivalve larvae indicate, for example, t. hat t 90 percent or more may survive passage. In assescAng impingemen t , it is assumed that all organisms which are impinged die. The prediction of the temperature increase in the thermal plune, which may cause mortality, is taken as the lowest temperature , indicated by available information as having an adverse effect. This te:rperat.ure may be the critical thermal maximum, tic LT,., or the lethal temperature (see Appendix A for an explanation'of these temperature criteria). That is, when information on all tempera tur e indices is available, the lowest among them is used. In projecting the effects of Units 1 and 2 operation, it is assumed that Units 1 and 2 will operate ct full load each day or i.I the yea r. [=g in predicting the effects of the thermal plume, and of lJ en tra.tnment and ispingement on the populations ot cer tain species, it is assumed that the organisms ef fected are members or locall:ed populations. This asstrnption tends to concentrate the of f eet and increase the predicted unpact. In situations where limitations in the present taxonomic ability pr eclude positive identitication to the species level, all I-1 I
I organisms belonging to the larger taxonomic category were assumed a to belong to the species being analyzed. This assumption also [ inflatos the ef f ect of the power station. cases the assessments of impact at the papulation level In most do not use the concept of biological compensation. This concept ( is the mechanism by which populations respond to exploitation and maintain a viable population. Therefore, the absence of R compensation in the impact assessment methodology results in an 5 overestimated impact. Di general, the assessments contai.u!. in the 316 Demonstration and this analysis are conservative and the actual ef f ects should probably be smaller than those predicted. Indeed, the field data collected during Unit 1 operation indicate that the actual ef fects are less than those predicted for Unit 1 operation. l The results of the studies conducted at the Pilgrim site have E been reported in the Boston Edison Semi-Annual Marine Ocology W Series, which presently consists of nine volumes. The list of ecological anc hydrolugical studies ass ociated with Pilgrim B Station was represented in Appendix B of the original July 197s W report. This material las been updated and is presentel in Appendix B of this supplemental report. The analyses which are contained in this report consider the t ef f ects of both the Pilgrim discharge and intake. Consequently, the analyses address both the Section 316 (a) and 316 (b) j requirements of the Federal Water Pollution Control Act W Amendments of 1972. The analyses also consider the ef f ects of Unit 1 and the combined ef f ects of Unita 1 and 2. Analyses are g reported for each of 13 representative impo rtant species g considered in the original 316 Demonstration report. The supplemental analyses, contained in the section of this report that follows the "Il ASSESSMENT" tab, are presented in a format ~ analogous to the July 1975 report. That is, the section and subsection numbers correspond to those used in the original re port for ease of cross-referencing with Section 6 or that re po rt . The sources of information specific to each representative g tmportant species are noted in the respective section for the 3 species. The information on the thermal tolerances of the representative important species, which was Appendix A in the i original July 1975 report , has been supplemented and is reported as Appendix A in this report. l The assessments of isotherm areas utilized in the "31o Demonstra-l tion for Pilgrim Nuclear Power Station, Units 1 and 2," issued in - l July 1975, were developed from centerline profiles contained in I the Pilgrim S tation Environmental Report. By utilizing the B distance along the centerline as the radius of a circle, areas E within which the plu. .uld be contained were determined. These were interpreted as .velope areas which would contain the plume 1-2 I
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but not necessarily be filled by the plume. eased on the
- consideration of the thermal tolerances of the representative important species , relevant isotherms were used in the analysis.
This supplemental assessment utilizes the same isothenn areas ao those described in the "316 Demonstration. . ." report. hefer to , g Section 2.2.3 of the "316 Demonstration..." report tor s 3 discussion of the plume characteristics. Later models of thera.al impact on the sea floor in the cite vicinity indicata that, under some low tide conditiot.s, the
'I 1.cttom of the plume will have a long, narrow configuration until plume detach:r.ent at around 1,000 feet from the discharge. Under 1.nfrequent conditions, plume detachment will not occur until some tarther distance. This plume configuration will move atout the sea floor as ambient tide and current conditions change, and the bottom area exposed to relatively consta nt exposure to high temperatures will be smaller than the isotherrn areas used in tnis supplemental asacssment. Isotherm areas based on this plume det.achment model are too conservative to be of use in biological analysis and therefore have not been used tor the following reasons: (a) the temperature tolerance data used for benthic I. species in this assessment are dependent on exposure time, (b) the isotherm areas already used are conservative in light of Unit 1 data which indicate detectable benthic damage in areas smaller than predicted, and (c) the plume will be mobile.
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SECTION 6 {i t lhPACT ASSESSMENT 6.1 Ph0CEDURES FOk ASSESS &,NT OF PILGRIM STATION 'S LFFECT ON SELECTED SPECIES
, impa ct. to each or the aelected species is assessed by the
- following strategy:
Data collt:cted from ecological studies at the Pilgrim site are
; reviewed with respect to the operating history ot Unit 1 (see i Appendix b tor listing oi field and laboratory stuciles) . The density of each of the belected species entrained, entrapped, or otherwise affected by the thermal cotcponent of the discharge or plant shutdown is then compared with availabic estimates of I species population densities. Information on lite history, geographic distribt.tlon , and thermal sensitivity is also considered to assess the sensitivity of the species population to L any etf ect of power station operation. Predictions of the etrects of Units 1 and e combined are made for t.he thermal plune, l' en t.raira.en t., and entrapment Ior all representative species based on these considerations.
Analyses of unpact are also based on hydrographic intormation (' whicn includes: (1) estanates of the maximum size of the thermal plume contacting the bottom (for assessment of potential thermal
, , ef fects for benthic species) ; the offects of the maxin.um mid-deptn and surface plume are also considered for assessment of I impact. on pelagic species; and (2) the projected maximum intake flow tor Units 1 and 2 combined (f or assessment of entrainment and entrapment impacts) . "I t
h quantitative representative species p;edaction of impact judged to potentially la presented for sustain soca i-l$ mortality from plant operation. The particular model used for "1 prediction depends 'tpon the information available to quantify the poptilation and ths perturbation . The models presented inlow are used for the quantitative predictions.
-I Populations for which the age specific mortalities and fecundities are estimated can be simulated by a computerizati on i of the Leslie (1945) model. This model is: '
I Nt+1 =AN - t (0
- I~l)
, where N is a 1-by-x vector corresponding t.o the nwnber of , . . , organisms (ni) in each of x lif e stages, and each lif e stage has an equal development time: 6.1-1 I
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- s. nc g (6.1-2) n t
.x -
The x-by-x A matrix in the projection matrix which describes the tranaition ot the population f rom tuo t to t+1
,I A= FiF2F3 Pt O O
....F) O x
F O x 3 O P2 0 R
. . . . O O O O Pi O O (6.1-3) B 5
O O O . . . . P)x O wnere F i is tlw number at remale offspring born to a female of agu i, P is the probability that an organism of age x will survive i to age x+1, P = e' i, " i (6.1-4) where d i is the instantaneous death rate of organisms of age 1. The finite rate of population growth (R) is calculated f rom the h matrix equation as the maximum characteristic root of the cha racteristic with the stable age distribution represented as the characteristic vector accompanying the largest root 1945) . (Leslie R = max char root 6 (b .1-5) I D b.1-2 5 E s
i The instantaneous population growth rate (r) is: , r = loge R (6.1-6) une method of investigating impact attributable to the power I station is to estimate the elements of the A matrix f rcru field and literature values i.or the affected population.. The value at r can then be calculattd. The Pi or the probabilities of I survival to the next age-specitic death rates. age can The then ' be converted to instantaneous instantaneous to entrainment can be acced to the age-specific death rate and mortality rate due I de new instantaneous death rates converted to a new age-specific probability of survivorship. The maximum characteristic root and the associated characteristic vector of the second A matrix represent the instantaneous population growth rate and the stable I age distribution of the impacted population. Instantaneous rates of population growth with and without [I - entrainment can be compared as can the stable age distributions. This represents comparinon of the theoretical potential of the population under the assumptions of exponential growth and is therefore most conservative as there is no densit*j dependence in
'I i the population. A computer program (END POP) was developed to numerically solve the characteristic roots and vector. This progra.n is based on the EISPAC routines contained in Reinsch and Wilkinson (1971) .
T The analysis of the year-to-year variation in population size is made by simulating the population represented by the Leslie (1945) model. A computer prograan (POPI) was also developed which simulat9s the Leslie model. This program calculates the
,T b procability of survivorship to the next age as the combination of the instantaneous rates of natural, fishing , and power station-related mortality. Any of the elements in the 6 matrix can be
',' g constants or functions of the population density. Tne population g is then simulated with and without the effect ot the power station. The change in popula tion size or any selected population parameter represents the ianpa ct associated with the power station ou fish eggs and larvae.
. '1he population methods presented thus f ar require a great deal of j information for the afrected population. Because ot the nature B of these parameters, it is dif ficult to estimate them f or field studies, and many times they do not exist Jn the literature. A simplistic approach is to translate the number of organisms lost
-.I Into the number of adults that would have resulted assuming no compensatory mechanisms (e.g . , density-dependent. parameters) in the population.
11 the population is in equ 2. librium , in one generation the tecundity or a breeding pair will be reduced to two breeding adults : t> .1 -3 I
2 . S.F (6.1-7) I where S is the survival irom egg to adult, F is the fecundity of a breeding pair during their life, or i S = 2/F (6 .1 -8) - If the af fected lif e stage is larval, then the survival f rom egg to larva (Se) is multiplied by F to give the survivorship from larva to adult (S1 ). o. s,.;e.,e, 2 (6.1-e) The number of affected larvae (N 1 ) is multiplied by S i to give the number of adults (N a ) that wbuld have resulted, asstraing no . density dependence. N a . S $N) ( 6 .1- 10 ) The number of adults can then be compared to some reference such as catch statistics for commercial or sport species. This is a meaningful comparison when sufficient inforn.ation is not available for the more extensive analysis. In addition to the assessments made by means ot the methodology described above, a number of topics have been considered in more 3 generic way. The following paragraphs discuss items which (a) do E, not lend themselves to quantitative evaluations and (b) re present sources of potential impact considered remote Ior the Pilgrim facility. g The erfects of exposing local fich populations to sublethal temperatures can incluae weight loss, premature spawning, larger 3 5 pr edator popula tions ruaulting in increased exposure to predation, and possible alteration of the natural predator - prey relationship. Substantial cublethal ef fects will ultinately be E manif ested as change in mortality or reproductive rates and any 3 measurable impact detecteo in data collected as part of the operational monitoring program. Such offects are unlikely to occur since the relatively small plume ui:e, the plume characteristics, and the behavior of tish suggest that local populations would be unlikely to reside for ext. ended periods of time in a portion of the thernal plumu with lethal or sublethal temperaturea. I s.1-o 3 m.
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1 I In some instances, the impact of thermal discharges can include alteration in t.he numbers or distribution of species which, any of a variety of reasons, could be classen as nuisance for 1 a species. As noted in Section 4.1.4 of the 316 Demonstration, two 5 nulaance aPecies trave been identified at the ptigrim site. The sea urchin (Strongylocentrotus droebachiensis) does teed on Irish noss among other macrophytes. However, it is a nonnelect.ive
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I predator and the field studies have not indica ted as direct relationship between operation of Unit 1 and the species distribution. Thus no alteration in abundance or distribution ot t 3 this urchin would be anticipatt.d after the start of operation of R tinit 2. Similar evidence can be cited for the red t.ide organism l- (Gonyaulax tamarensis) . Analysis of species composition and
'E abundance of phytoplankton collected from the Pilgrim Station g intake and discharge has not revealed any increase in Gonyaulax sp. In addition, other factors, such as salinity, light, and nutrients, may be more signticant than the effect of temperature l and would have to be within optimal ranges before a subs tantial increase could occur in the local population. Finally, even it temperature were a trighly signficant factor in the dynamics ot I
'i3E the population, the volume of the thermal plume is relatively small and therefore atf ects only a limited portion or the species population within a limited geographic area. lt might be posshble to consider the various epiphytes found on Irish moss as a nuisance torm. lionitoring in the vicinity ot {. Pilgrim has indicated changen in the degree ot epiphyt. ism over i the perica of the surveys. In general, the greatest d eg ree of epiphytium appeared in 1976, but there was no indication that r this was related to stat. ion operation since it occurred generally throughout the ntudy area. There was also some indication f rom [*E W the Irish moss survey that g_hond rus in the vicinity of the
, discharge was cleaner than that occurring elsewhere.
One other species which may be classed a nuiaance species as a result of changes in abundance or distribution is the green crab (Carcinus maenus). Field studies at Pilgrim have shown this
;. species to occur and to have somewhat higher numbers in the area of discharge. Because this species feeds on mussels and other
! bivalves, the mussel population in this area could be attected.
lionitoring at Pilgrim would suggest that such an effect does not occur. Despite the somewhat higher abundance at green crabs in the discharge, 1977 mussel densities were notably greater than I 1976 densities. In addition, the reproductive capacity ot mussels should allow for at least partial compensation tor any increased losses; neasonal recruitment from adjacent areas unaf f ected by any thermal plume related change would turther
- I compumate for localized density modifications.
beyond those effects on early life stages of various species I wnich are addressed in the following sections, it is possible that an indirect effect as a result of passive entrainnent into the discharge plume could occur. This would result trom small, I e . -s I L _
I planktonic forms which are incapable of signiticant movement being carried through the thermal plume. It is improbable that such entrainment would induce detectable mortality to species - af fected because (1) the residence time (and thus the exposure to g elevated temperatures within the plume) is very short, 3 (2) currents and tides in the area preclude the organisms from remaining near the discharge for an extended period, (3) the g maximum temperature elevation with both Unita 1 and 2 operating g is 230F, (4) the volume of water at the highest temperatures is very siall as a result of ra pid dilution, and (S) where available, thermal tolerance data indicate that early life stages of RIS will be able to tolerate temperatures found in all but the hottest portion of the plume (see discussions of eacn species in + Section 6.2 through 6.14) . There are no aquatic or terrestrial 3 species listed as threatened or endangered by the federal 5 government found or known to occur at the site itseli or in the marine environment in the immediate vicinity of the Pilgrim site. alof ouling control at Ptigrim includes use of a thermal tackwash. For Urtit 1, the backwash is discharged through the intake and ~ into the intake canal. The extent of the backwash plume has been ! monitored (Normandeau Associates, Inc., Thermal Surveys of '~ 3ackwashing Operations at Pilgrim Station during July 1977, . published Ln August 1977). This study indicated a relatively 3i thin plume that dissipated completely within a few hours. E. blulogic monitoring in the intake has indicated tne continued p esence of macrophytes including Lrish moss in the vicinity of t4 e canal despite backwashing. In addition , no impact such as a Mi'. g f.sh kill has been reported to result from backwashing for L it 1, and stopgates will be used in Unit 2 to limit or preclude - t; e release of heat from the intay' y during t e water heated by backwashing wil. backwash. Instead, be released through the d'scharae and this will be subject tf the normal dilution process "
- that point. This should ef f e ctiively eliminate backwashing g$.pAnUnit 2 as a source of impact to the intake area. !
h a number or instances above and in the following discussions, 3 daia obtained from surveys in or near Unit 1 have been us ed as g evidence pertinent to impact assessment for Unit 2. This is a reasonable approach not only because it provides cupirical evidence from an operating power plant, but because ( 1) there are numerous similarities in the intake design for th e two units, l~ (2) the units have a common intake canal and discharge, (3) the units are immediately adjacent, (4) the aquatic population B affected by operation ot the units is identical, and (5) source E and receiving water body eff ects of Unit 2 will be essentially the same as those of Unit 1. Difference 3 in impact tram Unit 1 g ana Unit 2 will result primarily f rom the increased flow of two g units as opposed to one and thus ertrapolation of quantified impacts on the basis of the flow differential is appropriate. g Overall, the approach of utilizing data for an existing intake to g determine potential ef fects of a proposed structure is consistent s.1-e I E E
w4th the suggested approach contained in EPA 31b (b) guidance u.anual (p. 26, 1 May version). A final general consideration as the effect that an intake approach velocity of 1 fps will have on fish impingement. As noted, the int.a ke design or Units 1 and 2 is very similar and I theretore evil ',ce can be gained from the screenwash monitoring of Unit 1. Tnese cata have been incorporated into the impact assessments for the RIS. In addition, some data are found in the i scientific literature on swim speeds of various fish species. In general, the data are limited but do indicate considerable
,, variatLon due to species, condition of the ilsh and physical i factors such as temperature. Evidence compiled in Table ?-59A ot I the Pilgrim t.h (p. 2-304A) indicates that for those species noted, each would be capable of swim speeds above the 1-tps approach velocity and thus should be able to move away from the traveling screens. ut course., thie would only occur arter the cI tish had traversed the intake canal where velocities are well belov 1 f ps and entered the intake structure. The low velocity l- i.n the intake canal reduces the potential for large numbers ot j
finh encountering the region of higher velocity in tront or the screens. To the extent that ettects due to the interaction of heat with other pollutants might occur, the conclusions in this assessment are surriciently conservative to account for them. m ( tl 3 m c
*e i
b*l-7
. 1 1
_1 6.2 IRISH MOSS (Chondrus crispus) I Irish moss is a subtidal species occurring from mean low water to about 30 feet below mean low water. It is, therefore, exposed to E temperature fluctuations but not to the degree of intertidal .f species. Primary station-related impact to Irish mosa may result from the thermal plume, because the moss ic a sessile organism. iE Entrainment of spores may occur, but should not affect a large E fraction of the spores since they are not buoyant. Impact assessment for Units 1 and 2 combined can best be determined by
- examining the historical data from Unit 1.
6.2.1 Thermal Plume Several studies have been conducted to determine the impact of atntion operation of Pilgri.m Unit 1 and Units 1 and 2 combined on [. the local Irish moss population. These include 1.nvestigations of 3 commercial harvest and effort by Mass 4 Division of Marine 5 Fisheries (MDMF) , thermal tolerance of spores by Marine Research, p Inc., benthic monitoring studies by Clapp Laboratories and by B Drs. A. Michael and R. Wilce, and short-term surveys of relative lj abundance and condition by J. Ryther et al, Woods Hole Oceanographic Institution. Generally, Chondrus crispus is found along the rocky Plymouth I coastline from Warren Cove to Manomet Point, with most of the commercial harvesting being done between Rocky Point and Manomet ,I Point. The most extensive beds occur at Rocky Point, Manomet B Point, and White Horse Beach, especially around Flag Rock (see Figure 6-1) . In 1973, there was a substantial decrease in the commercial harvest of Chondrus, with a concomitant decrease in effort f expended in harvesting (see Table 6-1) . The harvesters reported I the general condition of the moss as poor, which may account for the decreased effort and landings, though the catch per unit effort remained about the same as in previous years. By the fall p'g of 1974, landing statistics indicated that the Chondrus s population had recovered to normal or near normal conditions. 3 In order to assess the possible impact of Pilgrim Station on the
-5 noss, the shoreline was divided for study into eight areas. In addition, Ellisville (6 miles southeast of Manomet Point) and Gurnet Point (4 miles northwest of Pilgrim at the northern .I extremity of Plymouth Bay) were chosen as control locations.
Ellisville eventually proved to be a poor choice for a control location, having a sandy bottom covered with eclgrass, which I resulted in a moss population of poorer quality than that of the Rocky Point-Manomet Point coastline. Manomet Point also lies outside the predicted plume areas and-has, therefore, been used I as a basis of comparison (see Figure 6-2) for the 1971-1976 landing statistics from the Mass. Department of Marine Fisheries; landing statistics in lb-wet weight for Gurnet Point were not I 6.2-1 I.
I available to compare to wet weight biomass values from other a ar ea s . Dry weight biomass (lb/yd a) calculated f rom the relative E abundance and condition survey are shown in Figure 6-3 for Manomet Point, the discharge area, the intake area, White Horse Beach, and Gurnet Point. F.xamination of the 1974 survey findings failed to show power station-related ef fects beyond the area of exclusion. If the thermal plume adversely af fects the Chondrus beds, the greatest knpact would be expected nearest the discharge, dissipating as distance from the plant increases. This has not been observed to 3 date. From the western side of Rocky Point westward to Warren E Cove, the condition of Chond ru s criqpus increasingly dete riorated . Although restricted to a small narrow band of a rocky bottom, some of the most productive beds observed were in the discharge area, just beyond the area excluded to Chondrus g by the thermal plume. As usual, Manomet Point and the eastern portion of Rocky Point were good producers. Purthermore, for the remainder of the survey period (19 74 to 1976), these observations , held true. Pilgrim was operative most of 1975, and the 1975 surveys show overall continued improvement in terms of weight per unit area, though the quality ;f the plants seemed poorer . This poorer a condition was charact erized by less branching, lighter pigmentation, and increased growth of epiphytes on the Chondrus. 5 Still, as in the two previous years (1973 and 1974) , the plants of best quality were found between Rocky Point and Manomet Point, especially in the discharge area of Pilgrim; the poorest were found at Warren Cove. Pilgrim Unit 1 was non-operational from February to June in 1976, as in 1974; but, unlike 1974, which was a good year for Chondrus, 1976 saw some deterioration of the Chondrus beds. The g explanation is probably not related to thermal plume effects, but E more likely to natural phenomena . There was an increased incidence of epiphytes noted in 1976, such that plants everywhere (e xcept the discharge area) were heavily overgrown. This may explain the 1976 observations. Chondrus exhibits a large degree of natural variability in growth E and condition from year-to year and station-to-station, depending E on such factors as degree of oceanic exposure, silting, local topography, predation, and other phenomena which are not totally g understood. Natural fluctuations probably account for much of g the year-to year changes described above. The areas predicted to be seasonally affected by the two-unit thermal plume are shown in Figure 6-4 Because of faster mixing (due to higher discharge velocity) of heated and ambient waters, the increased thermal load generated by two units is quickly dissipated. Thus, the near-field isotherms ( 15 0 -20 0 F) for Unit 1 and for Unita 1 and 2 combined are very similar in size. 6.2-2 I E s
, a I
During summer, lethal temperatures cculd potentially exclude Chondrus f rom 2.1 acres in the intnediate discharge area. Because of the similarity of the plumes for Unit 1 and Units 1 and 2 just described, it is expected t. hat the predicted loss of 2.I acres closely approximates the 1.8 acres presently devoid of Chondrus. I In addition to the area lost to moss population, an approximately equal araa will contain moss with stunted growth, as evidenced by areas of stunted growth at Unit 1. 6.2.2 Entrainment - A study of the entrainment of Irish moss spores was conducted in the fall of 1973 by Marine Research, Inc. (dRI). Thermal tolerance tests, however, indicated that mortality (30 percent) e I of spores on passage through the station cooling system would occur only when ambient water temperatures were greatest, in late summer, when studies have found spore density to be low (tsI
- ' 3g 1975; Michael and Wilce 1975). Therefore, the overall effect of entrainment on the Irish moss population should be minor.
6.2.3 Entr pment Not applicable. 6.2.4 Cumulative impact r, Most of the i.mpact of station operation on Irish moss should !g result from the thermal plume. This localized eff ect will result
,g in the elimination of Irish moss immediately adjacent to the discharge area (2.1 acres) and an additional area of about ,a 2 acres having stunted growth. No impact will result f rom ig en tr apnent , as no life stages are susceptible to entrapnent.
Although entrainment raay occur, thermal tolerance tests on Irish moss indicate no impact of consequence from entrainment. Station g operation will result in a negligible effect on the tot.al Irish i moss population in the Warren Cove - Manomet Point area and on the commercial harvest.
.I I
I I I 6.2-3 I
TABLE 6-1 IRIS 11 MOSS 11ARVEST STATISTICS: 197i*-1976 (Mass. Div. of Marine Fisheries) Linding (lb-wet vt) Area 1971 1972 1973 1974 1975 1976
,. 1 92,637 133,402 57,045 105,110 79,652 72,950 2 78,060 110,246 45,310 91,290 89,614 125,140 3 10,719 17,295 4,140 11,730 16,487 25,250 1I 4 23,252 31,402 7,695 10,795 14,317 7.010 5 82,724 78,567 18,815 28,515 72,557 56,330
,g 6 39,925 56,881 24,995 17,230 74,417 24,280 3 7 14,727 17,004 30 215 10,517 2,320
- 8 33,429 28,368 605 25 3,252 235 Total 375,473 473,165 158,595 264,910 360,813 313,515 Earvest Effort thr)
.I ..
Area 1971 1972 1973 1974 1975 1976
'g
, 1 411.4 573.1 343.4 446.4 339.2 373.3 E 2 443.7 776.3 345.8 391.9 562.8 840.8 3 55.7 90.6 22.8 77.8 83.0 159.3 4 113.6 155.9 41.3 39.7 47.9 47.8 3
5 406.8 374.9 102.3 139.7 290.7 284.2 6 170.7 233.9 128.8 79.0 219.5 88.7 7 87.6 80.3 0.1 1.3 27.8 11.2 f 8 114.9 108.1 1.4 0.3 13.9 1.2 Total 1,804.4 2,393.1 985.9 1,176.1 1,584.8 1,806.5 Harvest Rate fib /hr) 3 Area 1971 1972 1973 1974 1975 1976 ig 1 225.2 232.8 166.1 235.5 234.8 195.4 2 175.9 142.0 131.0 232.9 159.2 148.8 3 192.4 190.9 181.6 150.8 198.6 158.2 4 204.7 201.4 186.3 271.9 298.9 146.8 5 203.4 209.6 183.9 204.1 249.6 198.2 I 6 7 8 233.9 168.1 290.9 243.2 211.8 262.4 193.7 300.0 432.1 218.1 165.4 83.3 339.0 378.3 234.0 273.8 207.8 201.5 Total 208.1 197.7 160.9 225.2. 227.7 173.5 I . 1971 values do not include appu tiniate 2-week perina print to l 6/ 18/71. l 1 of 1
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9 =- ;9's '97 19 7 , 1971 + 9 74 :9't t'; l f l! t m A4E ST A .'E apvtsT hes) E n;a7'-RS FIGURE 6-2 l COMPARISON OF ANNUAL IRISH r MOSS HARVEST STATISTICS AS RELATED TO M ANOMET POINT
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=- MAfJOME T POttJT RJ T A KE
- Otsocact FIGURE G-3
---- - conur i roinT COMPARISON OF IRISH MOSS DRY WEIGHT VALUES
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FIGURE 6-4 POTENTIAL THERMAL PLUME EFFECTS IRISH MOSS I,'
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I 6.3 ROCKWI:ED @scophyllum nodosum) Ascophyllum nodosure is an intertidal species and, therefore, is naturally exposed to large temperature fluctuations. However, as an intertidal species, it has a life history strategy which is adapted for these fluctuations. A continuous thermal stress, however, may result in stress during reproductive periods. A. nodosum is a sessile organism. Therefore, primary station-related impact to A. nodosum should result from the thermal may occur, although the spores are I plume. Entrainment nonbuoyant. Impact assessment for Units 1 and 2 combined is determined by analyzing data collected during Unit 1 operation. 6.3.1 Thermal Plume A benthic monitoring program conducted in *he vicinity of Pilgrim I Station by Clapp Laboratories, and subsequently by Drs. A. Plchael and R. Wilce et al, has determined seasonal biomass estimates for Ascochyllum nodosum at various transects. The two nost ecologically sim.tlar stations are the intertidal stations at the Manomet Point transect and the Rocky Point transect. Rocky Point transect is the area closest to the discharge with suitable habitat for Ascophyllum nodosum and, therefcre, represents the area most likely to be affected by the discharge. The Manomet Poi.nt transect is located sufficiently far away from the C. discharge to serve as a control location (see Figure 6-5) . Both areas represent moderately sheltered marine environments with gently sloping rocky shores that favor Ascophyllum nodosum. As such, Ascochvilum nodosum comprises 80-90 percent of the biomass at both stations (Michael and Wilce, 1975 and 1976). The mean intertidal biomasses for Rocky Point (discharge area) and Manomet Point (control area) are plotted in Figure 6-6. Each point on Figure 6-6 represents an average value taken from samples at the same location and time. Collection techniques for each date were the same for each location. The year-to-year biomass shows a slight downward trend at both Rocky Point and Manomet Point. If the power station were having an effect on Ascophyllum podosum, Figure 6-6 would reveal different time series of biomasses at the control and discharge stations. The
- more probable causes of density fluctuations are seasonal growth patterns and, possibly, subtle year-to-year variations in L.I sampling technique since both the control and discharge stations are changing in the same manner.
i L- As discussed in Section 5.2 for the 316 Denonstration, limited l information on the thermal tolerance of Ascochyllum makes
- l. prediction of the Unit 1 and the combined effects of the Units 1 I and 2 thermal plume difficult. However, operational data from
, Unit 1 indicate no significant impact (Michael and Wilce 1976) . l The average plume temperature outside of the discharge canal will
- I 6.3-1 I _
I generally not reach 930F during any season; therefore, acute g mortality should not occur (refer to thermal tolerances in 3 Appendix A). Since thermal tolerance during reproductive periods has not been studied, the possible effect of Pilgfim Station on a reproduction is uncertain. Ilowever , da ta gathered at Unit 1 g indicate minimal impact since, for the more than four years that As cophy11um nodostrn has been monitored, there has been no apparent station-related effect (see Figure 6-6) . 6.3.2 Entrainment Zygotes, the only entrainable life stage of A. nodosum, are nonbuoyant and adhesive and thus are not expected to be subject to entrainment. No 6. nodosum zygotes have been collected by MRI in entrainment samples . 6.3.3 Entrapment Not applicable. 6.3.4 Cumulative Impact No station impact on A. nodosum is expected to occur through entranment or entrainment, since no life stage of this species is E susceptible to these sources of imt<et. The only potential g, source of impact is the thermal plume. The upper lethal temperature of A. nodosum ( 33aF) will not be reached in the discharge plume of Units 1 and 2; mortality is expected. therefore, little, if Reproductive periods occur from fall through spring when discharge temperatures are low; therefore, no any, l* impact is expected during these periods. Operational data g collected at Unit 1 have also not shown any station-related W5 effeet to date. I I I I I I 6.3-2 I E a
\ CuRNET PT h $ n0C<v 90? TOW s?AfiC% 8 3 SAND stations I.
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FIGURE 6-6 MEAN INTERTIDAL DENSITY ASCOPHYLLUM NODOSUM 2 IN DRY WEIGHT (G/M 3 Q
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1 . I 6.4 AMPHIPOD (Acanthchaustorius millsi) I Acanthchaustorius millsi is a subtidal burrowing amphi a l - found of fshore of Pilgrim Station. As an offshore species, A. adllsi I is less subject to power station effects than inshore species. The component of power station impact that will most affect A. millai is the thermal plume. No A. millsi have been collected in entrainment samples, and the species is too small to be I entrapped . Impact assessment for Units 1 and 2 combined can again be determined by using th e information collected during Unit 1 operation. 6.4.1 Thermal Plume I Results of the Unit 1 benthic monitoring study have been reviewed to determine the impact of station operation on A. ndllsi. densities at 20 feet below mean low water mdw) at the discharge Mean ig location and White Horse Beach (control) are compared in 3 Figure 6-7a. A second comparison of the control and discharge r for 30-foot stations is presented in Figure 6-7b, since the ! 20-foot stations were not sampled after 1974. Densities of A. millsi are highly variable at White Horse Beach and di scharge locations. There are several factors which may contribute to this variability. 6 millsi is motile and can thus avoid sampling devices. Also, the preferred habitat at the discharge sampling area is somewhat limited because of the presence of l rocky areas. This would also contribute to the lower density at 'h3 the effluent station, as compared to White Horse Beach. reduced preferred substrate, collections at the discharge would With be more subject to variability through clumping, and thus a nonuniform distribution of organisms. This type of variability commonly occurs in short-lived species that reproduce only once. { The thermal plume will rarely contact the bottom beyond a L distance of 1,000 feet from the point of discharge (see Section 2 of the 316 Demonstration). The depth in this area is approximately 20 feet below alw. When the plume does contact the h bottom, only the 20F and 30F isotherms may reach this area. The 5 habitat inshore of this area subject to higher temperature increases does not appear to be suitable for A. millsi, as it is primarily a rocky substrate. The thermal tolerance of A. millsi
'I appears to be high, although it is a subtidal species.
Temperatures as high as 970F are necessary for complete mortality, and the temperature .nortality range appears to be I small (Sameote 1969) . Therefore, no impact is expected, since temperatures habitation. will not reach 970F in areas of A. millsi 6.4.2 Entrainment Not applicable. 6.4-1 I - _ . . _
I 6 ~. 4 . 3 Entrapment Not applicable. , 6.4.4 Cumulative Impact No station impact on & millsi is expected to occur through entrapnent or entrainment as no life stage of this species is susceptible to these sources of 1:: pact . Tne only potential source of impact is the thermal plume. Suitable habitat for A 2 millsi in the discharge area begins at 20 feet mlw and extends into deeper water, which is beyond the major influence of the predicted thermal plume. Therefore, there should be no impact on h millsi as a result of the operation of Unit + 1 and 2. I I I . w I I I-I e.o-2 I 5
l . I
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- r. 1971 1972 1973 1974 PREC DER AT ION AL r' - OPER ATION AL ri c
,u' c opt. R . . ATiON AL PLUME AR E A (ROCKY POINT)
----- C ONTROL AREA (WHITE HORSE BEACH)
I mere e.. ME AN DENSITY OF I ACA N THOHAUSTORIUS MIL L SI AT 20 FEET BELOW MLW l I
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I e 1 I s 1 o I I r i .__ , O I I I I ' 'I I ' I I I I ' ' ' ' I I ' AUG WOW FEB af AY AIAi NOV FEB M A T' As A') fvtyv Ffs M AY S(Pt h0V FEB MAf AtsG OCT FES APR JUN 1971 1972 1973 1974 19 75 r976 ret ort p AY eoNAL rf O P E '4 AT IOm a t rfr0 P['5 5 ONAL = = '*L + \== =s, j p ,, , Ne wcet r.a rsom at. / \ cPr natiomat r------z CONT HOL ARE A (W4ITE HORSE BEACH) EF FLUE t41 FIGURE 6 7b MEAN LENSITY OF ACANTHOHAUSTOR!US M/LLSI AT 30 FEET BELOW MLW -6 _ _ _ _ .._-
1 6.5 AMERICAN LOBSTER (Homarus americanus) The lobster is a subtidal, mobile benthic species found of f shore of the Pilgrim Station. As an offshore species, lobster are less
'I subject to power station effects tnan inshore species.
Monitoring studies at the site by the Mass. Div. of Marine Fisheries (MDMF) , have indicated that the local population of lobster is _ not a self-sustaining population and relies on
-I spawning elsewhere in Cape Cod Bay . Morrissey (1971) indicated that there was some movement of egg-bearing females from the I northeastern shore of Cape Cod to this area. About 310 of 45,759 lobsters or about 7 in 1,000 handled during the 1972-1976 studies were ogg-bearing females. Thus, the local population in the vicinity of Pilgrim Station is a nonsustaining population.
.I 6.5.1 Thermal Plume Two monitoring studies by the MDMF have been conducted to i determine the impact of station operation on lobster. A harvest-per pot study monitored lobster catch within grid areas (Figure 6-8) in the vicinity of the station. Figure 6-9 shows the catch per pot f or grids in the discharge area and catch per pot at Manomet Point { control area) . There are no apparent station-related eff ects since such stresses would appear as non-parallel time paths of the control and af fected areas.
A second study monitored lobster migration in control and affected areas. The discharge area did not seem to present an unmanageable stress on lobster because the patterns of migration were similar for Rocky Point (discharge areal and Manomet Point (control area) . The seasonal effects from the predicted thermal plume (Appendix A) of Units 1 and 2 are shown in Figure 6-10. Based on ~ thermal tolerance data for lobster (Appendix A) , permanent residence of adult and juveniles will be excluded from the area (2.1 acres) immediately adjacent to the discharge canal during the summer months. The area beyond will maintain temperatures promoting (68 0-778F) maximum growth for adults and juveniles during the summer months. During other seasons, the temperature E will stimulate growth in the summer exclusion area (150 F 5 isotnerm). Growth of lobster to harvestable size has been reduced from 7 to 2 years in some heated waters (Hughes et al 1972). Lobster are mobile and can thus migrate to the thermal
. plume when temperatures are suitable , and migrate out of the thermal plume if temperatures are less than optimal.
6.5.2 Entrainment Prior to 1975, no lobster larvae were collected in the I entrainment study by MRI at Pilgrim Unit 1. Therefore, the original 316 Demonstration utilized a very conservative approach, I 6.5-1 I
I I assuming that the density of lobster larvae entrained was the same as the density of lobster larvae in the Bay near Pilgrim. In 1975, a modified entrainment sampling program by MRI was g initiated. As a result of this modified program, one larva was 5 collected in the entrainment studies at Pilgrim during 1975 and two were found in the 1976 studies. The analysis in this supplemental report is, therefore, based on these recent entrainment figures. Based on an extrapolation of the two lobster larvae collected in the 1976 Unit 1 entrainment study, an estimate of the total number of larvae which would have been entrained during operation of Units 1 and 2 was developed by integrating through the sampling dates before and af tc-r each of the lobster larvae were collected. A linear extrapolation between sampling pc.ints was utilized. This projection was a bout 24,000 lobster larvae entrained for full time operation of Units 1 and 2. The number of adults that could have been recruited into the adult population f rom 24,000 larvae is calculated as follows. After determining the number of larvae potentially entrained, the equivalent number of eggs from which 24,000 larvae would have survived is computed. Assurt . a survivorhsip of 0.01 from eggs ; to stage IV larvae, the equiva knt of 2,400,000 eggs would have been entrained. An estimate of loss of harvestable adults (see - Section 6.1) assuming 100 percent entrainment mortality can be made based on average harvest size (1.2 lb) and fecundity (10* g eggs / female) for this year class (Saila et al 1969) g. N" (no. of adults) = 2.4 x 106 enca x 10-* yr females x 2 adults y 490 adults egg female I This estimate, although based on conservative assumptions, is the most reasonable estimate of the ef fects of entrainment on the lobster. The number of harvestable lobster potentially lost g represents about 0.07 percent of the average yearly harvest for 3 Plymouth County (Beals et al 1970) . 6.5.3 Entrapment Prior to 1976, lobsters were not collected in the impingement nonitoring study. In 1976 four lobsters were collected from the intake screens during 2,022 hours of monitoring. Assuming the number impinged is proportional to the volume of water withdrawn, g 23 lobsters could have been entrapped in 1976 by Unit 1 and 98 3 entrapped by Units 1 and 2 if Units 1 and 2 were operating continuously. Impingement monitoring study data (particul arly from other marine organisms) suggest that a linear prediction is highly conservative. Therefore, entrapment of lobsters will be negligible when Units 1 and 2 are operating. 6.5-2 I Il
I I 6.5.4 Cumulative Impact Minimal impact on lobster is expected due to entrapment because i very few (4) have been collected during 4 years of Unit 1 operation. Based on- thermal tolerances during the summer months, adult and juvenile lobsters will be excluded from 2.1 acres imaediately ad jacent to the discharge canal. During the spring and fall of the year, growth should be stimulated within this area. Since
)d lobsters could avoid less than optimal temperatures, no mortality as a result of the predicted thermal plume is expected. !- Entrainment figures indicate about 24,000 lobster larvae, or about 490 adults, per year potentially entrained by Units 1 and 2. This number of adults represents only about 0.07 percent of the Plymouth County harvest. Considering these predictions and the conservative assumptions used, the offeet of the operation of Units 1 and 2 in the Cape Cod Bay lobster population should oe negligible.
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p, 6.6 BLUE MUSSEL (Mytilus edulis) Mytilus edulis, due to its life history and distribution, is j adapted to extreme environmental conditions, including a broad and exposure to partial drying. Station W range of temperatures F -impact would result from the thermal plume on adult organisms and entrainment planktonic larvae. Potential impact of Units 1 I of and 2 is assessed using the information obtained during Unit 1 operation. 6.6.1 Thermal Plume The benthic monitoring program that surveyed Ascophyllum nodosum ! 'E and other species of the algal community considered in the E 316 Demonstration also encompassed a faunal survey including r quarterly monitoring of Mytilus. Because most of the mussels collected for sampling were very small (1-3 mm), positive 3
~5 identification of species was not possible. Since adult Mytilus edulis is usually found in intertidal zones, while Modiolus modiolus is found subtidally, it was assumed that all int ertidal specimens were Mytilus edulis. Mytilus densities for 1971-1976 are shown in Figure 6-11. Although there are large fluctuations, F this is common in intertidal communities. No station-related !'N effacts are apparent, since such stresses would appear as non-W parallel time paths of the control and affected areas.
g The seasonal ef fects of the predicted thermal plume compared to thermal tolerances (based on Appendix A) from Units 1 and 2 are
'E shown in Figure 6-12. The greatest density of Mytilus occurs ' within the 10-foot mlw contour. A higher ambient temperature , (maximum seasonal surf ace temperature) is used for the discussion of-Mytilus than for the previous sub-tidal species since an elevated- temperature is more representative of the intertidal
[ environment. - During maximum ambient temperaturee reached in summer, the o thermal plume will have two primary effects on the mussel i population (see Figure 6-12) : lethal temperatures within the 100F isotherm will affect approximately 4.9 acres; also, critical E thermal maximum (CTM) may be reached in an additional 7 acres as
!; evidenced by anticipated aberrant behavior of the mussels. In this area of CTM, the mussels may cease feeding for brief periods, though no mortality is expected. Furthermore, Pearce 750F normal attachment, movement and
.I (1969) reports that aggregation of Mytilus is inhibited.
at The byssal fibers by which mussels attach to the suberatum fail to tightly hold the mussels, even when disturbed. Although this water temperature E,3 B also impedes feeding activities of such mussel predators as the seastar , green crab, and the whelk , the population may remain vulnerable to foraging iinfishes. In the fall, the aret. of
- a of CE
,g trortality will be about 1 acre, and the area about 1.2 ocres.
I 6.6-1 E
I 6.6.2 Entrainment Da ta have been gathered by MRI during 1974, 1975, and part of 1976 to determine the number of Mytilus la rvae entrained at 3 Pilgrim. However, it was not always possible to identify species 5, of mollusks during early stages of development. Therefore, for this analysis, all bivalves were assumed to be Mytilus edulis. Thus , the evaluation is conservative . The da ta gathered for 1974 through 1976 are plotted in Figure 6-13. By integrating over the period of occurrence formed by the data sets of 1974 and 1975, the number of larvae entrained per year can be calculated. The estimates were calculated by trapezoidal integration for Unit 1 alone and are 6.68 x 1011 g entrained for 1974, and 5.78 x 1012 entrained f or 1975. For both 3 Units 1 and 2, estimated entrainment is 2.21 x 1082 for 1974 and 1.91 x 1013 for 1975. According to Purchon (1968), natural mortality of bivalve larvae to adults is 99.9 percent. Applying this mortality to Mytilus, I the larvae entrained by Units 1 and 2 might have produced 2.21 x 10' a.dults in 1974, and 1.91 x 1010 adults in 1975. The average number of adult Mytilus for Rocky Point and Manomet g Point intertidal stations combined is 8,537 per square meter. g. Using the above entrainment figures, this would be equivalent to 2.6 x 105 and 2.2 x 106 square meters or 64 and 544 acres of Mytilus edulis for 1974 and 1975, respectively. ; As suming 100 percent entrainment mortality and that all bivalves are Mytilus edulis makes these estimated losses highly conservative. Theoretically, 19.3 and 167 acres of Mytilus (for 1974 and 1975, respectively) should have been lost as a result of Unit 1 entrainment. In general, no detectable change in Mytilus 3 density has occurred as a result of Unit 1 operation (pe rs . E comm . , Dr . A . Micna el , 8-15-7 7 ) . 6.6.3 Entrapment Mussels are commonly collected f rom intake screens; however, they are not considered entrapped species since they actively colonize the screens rather than being pa ssively swept onto them. 6.6.4 Cumulative Impact No detrimental station impact on M. edulis is expected to occur l through entrapment, as this species readily colonizes intake 3 l scree ns . However, the reason for biofouling control which 5 l includes chlorination and thermal backwashing is control of mussels in the circulating water system. Therefore, potential station-related effects on M. edulis can result from the thermal plume and entrainment. 6.6-2 I l E a
l Based on thermal tolerances, some mortality may occur in summer within the 100F isotherm (4.9 acres) and within the 200 F isotherm (0.9 acre) in fall. In addition, approximately 6.8 acres of Mvtilus in summer and 0.9 acre in fall may sustain increased predation and temporary cessa tion of feeding as a result of thermal effects. 5 5 Entrainment of M. edulis larvae will occ _r during operation of Units 1_ and 2. The predicted entrain:1.ent numbers are 2.2 x 101z for 1974 and I 1.9 x 1013 for 197 5, based on Unit 1 sample data. Conservative estimates of equivalent acreage lost through entrainment (assuming 100 percent mortality) are 64 and 544 acres for 1974 and 1975, respectively. More realistic but still conservative estimates based on entrainment mortality studies by P MRI (1975) (assuming 10 percent mortality) are 6.4 acres for 1974 and 54.4 acres of Mytilus edulis lost for 1975. B Based on the above estimates, the large size of Cape Cod Bay, and rapid colonization of M. edulis, the cumulative impact of Units 1 3 ~g and 2 operation on the population of M. edulis will be g negligible. L3 I iLg I LI I L3 I 6.6-3
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OBSERVED AT UNIT I 1974 THROUGH 1976 I
i (. I 6.7 COMMON PERIWINKLE (Littorina littorea) F Common periwinkle is a dominant intertidal gastropod at Pilgrim
!Eg station.
temperatures It is a eclerant organism adapted to and partial drying. Power station-related impact varying could result from the ef fect of the thermal plume on adults and entrainment of planktonic eggs and larvae. As in previous I discussions, the potential impacts of the combined Units 1 and 2 diccharge are described by relating results of monitoring studies at Unit 1 to the predicted Un,its 1 and 2 discharge data. 6.7.1 Thermal Plume 3 As for Mytilus edulis , intertidal densities of Littorina littorea 3 have been measured quarterly as part of the benthic monitoring
, stuoy. Data collected between 1971 and 1976 are plotted in a
a Figure 6-14 No station-related effects are apparent since g station-related stresses would appear as non-parallel time paths of the control and affected areas. Due to the high thermal tolerance of Littorina littorea (see Appendix A) , no thermal i_ impact is expected. r 6.7.2 Entrainment
!h3- Due to difficulty in species identification, all gastropod eggs and larvae are assumed to be Littorina littorea. Egg and larval
- samples have been collected by MRI for 1974, 1975, and part of L 1976 (see Figure 6-15) . By integrating over the period of occurrence (formed by the data sets of 1974 and 1975), the number
! of larvae entrained per year can be estimated. The estimates were calculated for Unit 1 alone, and for Units 1 and 2 combined.
The estimates are:
- 1974 1975 L
Unit 1 Units 1& 2 Unit 1 Units 1& 2 4 h_ No. eggs entrained: 8.7 x 1080 2.9 x 1011 8.1 x 1010 2.7 x 1011 l No. larvae i entrained: 4.3 x 1010 1.4 x 1011 3.2 x 1011 1.0 x 1012 jg lc The projected larval entrainment is high relative to egg
-m entrainment . This is because larvae are planktonic for a bout a 6-week period but eggs are in the water column only 6 days.
2 3 Thus, there would be a greater opportunity for larvae originating
'g . outside the station area to be entrained by Pilgrim Station than for eggs to be entrained.
I As a conservative estimate of localized impact, the number of larvae entrained will be included with the number of larvae normally expected to survive from the entrained eggs. Assuming 6.7-1 I
I 0.1 survivorship of eggs to larvae, this totals 1.69 x 10ti entrained for 1974 (2.9 x 1010 + 1.4 x 1011) and 1.0 x 1012 larvae entrained for 1975 (2.7 x 10 8 0 + 1.0 x 1032) for Units 1 and 2. Applying 99.9 percent mortality of larvae to adults (Purchon 1968), the above eggs and larvae would have produced 1.69 x 10e 3 and 1.0 x 10' adults in 1974 and 1975, respectively. The average 3 number of adults at Manomet Point, the station farthest from the discharge, is about 380 per square meter. Using the estimated number of adults lost due to entrainment, an equivalent area lost would be 110 acres in 1974 and 668 acres in 1975. This estimate is very conservative since all gastropod larvae E were assumed to be Littorina littorea, and larval entrainment 5 mortality was assumed to be 100 percent. In fact, larval entrainment mortality is probably less than 10 percent (MRI g 1975). Using 10 percant mortality, a more reasonable estimate 3-would be 11 acres lost in 1974 and 68 acres lost in 1975 as a result of Units 1 and 2 opera tion . Theoretically, 33.6 and 213 acres would be expected lost in 1974 and 1975 from Unit 1 operation. To date, no detectable change in Littorina density has occurred as a result of Unit 1 operation (pers comm. , Dr . A. Michael, 8-15-77) . 6.7.3 Entrapment Not applicable. i 6.7.4 Cumulative Impact No entrapment of L. littorea is expected because no life stage is susceptible to this source of impact. Potential station-related , effects on L. littorea may result f rom the thermal plume and entrainment . Based on -thermal tolerances, no thermal impact on Littorina g littorra is anticipated. Entrainment of both periwinkle eggs and E larvae will occur; based on entrainment monitoring at Unit 1, 1.69 x 1011 and 1.0 x 1012 larvae would have been entrained in 19 74 and 1975, respectively, as a result of two--unit operation. If all larvae entrained are assumed lost, a conservative estimate of equivalent adult acreage lost is 110 acres for 1974 and 668 acres for 1975. Based on entrainment mortality s tudies , a more realistic estimate using 10 percent entrainment mortality would be 11 and 68 acres lost for 1974 and 1975, respectively. Based on the above conservative estimates, the large area of Cape Cod Bay, and rapid colonization of L. littorea, the cumulative impact of Units 1 and 2 operation on the Cape Cod Bay population 3 of L_. littorea (the equivalent of approximately 25 acres) will be negligible. g o.7-2 5
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JAN FEB MARCH APRIL MAY suNE Juu AUG SEPT OCT Nov OEC tl F' , L FIGURE 6-15 DENSITY OF L/TTORINA i --- ll7[ 7 (GASTROPOD) L A RVAE 1974 OBSERVED AT UNIT I 1974 THROUGH i976 I
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I 6.8 ATLANTIC ME.NHADEN (Brevoortia tyrannus) r The effect of the operation of Units 1 and 2 on the Atlantic menhaden (Brevoortia tyrannus) population is predicted by a population simulation model. Sources of impact to this population include entrainment of larvae, impingement of 7_
; yearlings, and the effects of the thermal plume, such as gas I bubble disease to adults. The banis for the analysis of impact is a population dynamics simulation model initially developed by Schaaf and Huntsman (1972). The model was uned to simulate menhaden populations for a 50-year period. The analysis also r.
I included additional sources of mortality representing the power station operation effects. Results of both simulations were j compared with respect to population si::e and the projected yield to the commercial fishery. 6.8.1 The Model The menhaden life cycle model used f or this analysis allows prediction of future population structure. A Ricker (1958) stock g and recruitment function from Schaaf and Huntsman (1972) was used
'g to predict the number of fish in age-class 1 (R) from the total number of spic, ers (S) the previous year:
K = S exp (1626 - S/106)/654 (5.8-1)
. The stock, and recruitment function is the density-dependent component in this population dynamics model. A craph of the function is depicted in Figure 6-16. For spawning densities r below 6.54 x 108, an increase in the spawning stock results in an ;g increased number of recruits. For spawning densities above 'g 6.54 x 10e, an increase in the spawning stock results in a decreased number of recruits.
The instantaneous natural mortality and fishing mortality were assumed to be constant for all 10 age-classes. The instantaneous fishing mortality of age-class 1 was calculated as 66 percent of the fishing mortality of the other ages (Table 6-2) . The simulations were run with a natural mortality rate of 0.37, as r, developed by Schaaf and Euntsman (1972). The instantaneous l g fishing mortalit y rate of 0.8 was used. Schaaf and Huntsman E (1972) determined that this fishing mortality rate results in annual commercial atches of 400,000 to 500,000 metric tons.
- m. Yield to the r.ommercial fishery was calculated using the -
exploitation formula: U = F (1-e") /Z , (6. 8 -2) where U is the exploitation rate, F is the instantaneous fishing mortality, and I is the total mortality rate from all sources.
.I 6.9-1 I
E The yield is calculated in metric tor.s by using avarage weight at l each age-class from the data of Reintjes (1969) and is presented W in Table 6-3. The number of fish which incur mortality from the power station is also calculated using the for nula (Eq . 6. 3-2) by
.t h tituting the instantaneous mortality rate due to the power Mon for F.
- The effect of the power plant was simulated by first calculating a mortality rate due to power plant-related events (e .g . ,
entrainment, entrapment, and plume ef fects) . Entraitenent data were' collected for 1974, 1975, and 1976. The numoer of larvae entrained in any one year at Unit I was calculated by integrating the curve formed by density values determined during the period of entrainment for that year. To predict the offects of two-unit operation, the estimate was then multiplied by the ratio of flow of Units 1 and 2 to the f]'.)w of Unit 1. (See Table 6--4 for m:mbers of larvae entrained.) To estimate the mortality rate which would result if all l entrained larvae were lost, the number of larvae produced by the simulated population was calculated. The age-specific fecundity for menhaden was estimated from the weight-fecundity relationship of Higham and Nickoison (1964). g; The age-specific mean weight from Reintjes (1969) was then used 3, to obtain the age-specific fecundity (Table 6-2) . The equilibrium population (see Table 6-4) wa si multiplied by the fecundity to obtain an estimate of the number of eggs produced. I-It was assumed that 1 in to egos hatch. This results in an ' estimated 1.45 x 1013 larvae. The estimate of entrainment mortclity ist Me = -in (1-(no. of eags
- 10+ no. of larvae entrained in a year /
1.4 5 x 1012)) (6.8-3) The effect of impingement of menhaden on the traveling screens was estimated from the screenwashing data collected from 1973 to 1976. Menhaden impinged were not distinguishable from other clupeid species for 1974-1975, therefore, it is conse rva tively assumed for this analysis that all clupeids are menhaden. It is also assumed these fish are age-class 1, since they are unidentifiable as menhaden. Numbers of fish entrapped per year have been estimated for 1974 3 to 1976 (see Table 6-5) for one-unit operation, ar,suming that the 5 power station runs continuously throughout the year. The prediction for two-unit operatJ.on assumes that the number of fish l e.itrapped is proportional to the rate of flow (a conservative l assumption). The estimated additional mortality to the l population would be: MI = -in (1 - no, impinged in a year,2.92x10' (no. of age 1 fish)) (6.8 4) 6.8-2 5 s
I Tne gas bubble disease-related mortality is I effect of conservatively predicted by calculating the additional mortality r t. hat would have resulted from a kill of the size which occurred at Pilgrim Unit 1 in April 1973, and i'rposing this additional uortality each year. Since this mortality does not occur every year, as eviderced by 1974, 1975, and 1976 data, this estimt te is nost likely an overestimate. The 1973 fish kill has been estimated to be about 43,000 eJe ' fish. In 1975, a smaller f ish kill estimated at aceut 5,000 menhaden took place. The additional mortality to the I equilibrium-simulated population based on the higher 1973 kill would be: l ng = -In (1 - 4.3x 10 */3.5x 10 8 (no. age 3 fish)) = 1.23x10-*
! The nortalities attributed to the power station are added I singularly and in combination to the total mortality rate and the population re-simulated. The number c,f fish which sufter nortality due to the power station and the percentage of the equilibrium population affected were also calculated from the simulation.
I' The initial population structure and size for the simulation analysis was calculated based on the data from Schaaf and Huntsman (1972) for the year 1955. This estimate of population size was calculated f rom the number of fish in the commercial catch and the 1955 age-specific exploitation rates (Table 6-2) . [1'E The exploitation rt.te for age-class 1 was two-thirds the average exploitation rate
, for fish ages 2 to 5- For fish 6 years and older, the average exploitation rate was used.
6.8.2 Results of Thermal Plume, Entrainment, and Impingenent
- The population sf.mulation of menhaden with the parameters listed in Table 6-2 revealed a population which reached an equilibrium size of 4.48x10' individuals and a stable age distribution (Table 6-3) . At equilibrium and an annual fishing nortality rate
EE of 36 percent, the yield to the conenercial fishery is 3.94x105 metric tons. "
The results of imposing additional mortality to the population to simulate the effect of entrainment, entrapment, and the ther nal discharge are presented in Table 6-6. The result of imposing an
,;I additional mottality due to entrainment is a population which comes to an equilibrium and is reduced in size by 0.00003 to r 0.0003 percent f rom the non-impacted population.
The simulation of and the thermal effect reveal entrapment similar levels of reduction in population size. These simulations also produced populations which reached an equilibrium. I 6.8-3
I The combined effects of all three sou"ces of power plant nortality were simulated f or all three years. The resulting p>pulation had stable equilibriun and population si::os 0.0007 to 0.001 percent below the non-impacted population. 6.8.3 Cumulative impact The simulation performed using the population dynamics model of E Schaaf and Huntsman (1972) reveals a population ich is g regulated only by the stock and recruitment function. .he other population parameters which include age specific individual weight, natura' and fishing mortalities are constants regardless of population density. Imy perturbation to the population within several orders of nagnitude of that estimated for the pilgrim Nuclear Power Station, Units 1 and 2, results in a change in the equilibrium l population density, but not the stability of the equilibrium. It g is . difficult to predict the reduction in the Massachusetts g menhaden catch as a result of the operation of Pilgrim Units 1 and 2, since Massachusetts does not represent a biological sub-unit of the North Atlantic menhaden population. An estimate in the reduction in Massachusetts catch could be made for the fish which were Ailled by entrainment, entrapment, and the effects of the thermal plume if these were assumed to all be translated into reductions in the Massachusetts catch. These losses due to power station events n'ay be compared to the 3 yield to commercial fisheries. W e landings of menhaden in all 3 Massachusetts ports and the dollar value of the landings are presented in Figure 6-17. A loss of 43,000 age 3 fish which was ! estimated for the 1973 fish kill would nave represented 0.11 p.ercent of the 1973 Massachusetts catch, or an approximate dollar value of $944. . An estimate of the reduction in the commerc/ al fishery catch as a result of power station operation (due to ai l, three sources of mortality) was made for a constant rate ' fishing morr.ality. The worst-case reduction in the North Atlantic catch in the impacted population vs. the non-a f fected population is about 53,000 fish per year, a 0.001 percent reduction. If it is further assumed that the reduction in Atlantic menhaden population si::e of 0.001 percent is represented by fish weighing about one pound each, the weight of this loss is then 24 metric tons. This corresponds to about 0.13 percent of the 1973 nasaachusetta catch, or a dollar value of about $1,119. I I 6.8-4 a
k TA1112 'i-2
.t
[' PARAMETERS OF MENilADEN POPtilATION SI14UIATION MODEL r instantaneous Instantaneous Average i , e- Natural Fishing Weight Class Mortality . Mo rt a l i t y,_ Mrams) Focundity 1 0.37 0.53 127.3 - I 2 3 4 0.37 0.37 0.37 0.80 0.80 0.80 270.5 488.2 600.0 239,845 345,976
'E $ 0.37 0.80 689.1 408,269
;3 6 0.37 0.80 762.0 459,23'l 7 0.37 0.80 793.6 481,330 8 0.37 0.80 039.5 513,420 I- 9 0.37 0.80 839.5 513,420 10 0.37 0.80 839.5 513,420 k
i t og ft at og "I i l
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1 TABLE 6-3 SI.MULATED EQUILIhRIUM 01" MidillADEN TCPULATION
,E Populat. ion Age Yield 3 Aa o-Cla s s Si zo (x 1061. Distribution 1 Metric Tons) 4 2,815.9 0.629112 125,270 I
1 2 1,144.8 0.255780 146,030 3 355.32 - 0.079386 75,096 l 4 110.28 0.024639 31,201 5 34.227 0.007647 11,122 6 10.623 0.002373 3, 8 12 7 3.2970 0.000737 1,234 I 8 1.0233 0.000229 405 9 0.3176 0.000071 125 10 0.0986 0.000022 39 Total 4,475.9 1.000000 394,334
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E N E E N' E O M M@ E E E E TMCE 6-5 PFIT*1LM TJ'RFFS Or FIG IMPtw2D 197et'D 19F5 1986888 1973 tpt i t s 15 2 Urti t 1 Units 1& 2 Unit 1 thit s 1 & 2 Unit 1 Unit s 1& 2 Unit 1 6,175 19,172 2,402 18,454 100 905 Atlant ic menhaden 8 8 8 14,698 47,094 642 to 51 % 172 128 Wanter f loeter 415 1, hd 1,520 17 61 0 0 302 Pollock, % 334 2,299 7,337 2,927 87 2% 4% 1,514 Ozzmer 824 3M 602 2,746 2,181 7 s31 tw 72s 91 Reintesw smelt 7 %9 894 2,8 20 491 2,392 Atlant ic silwrsida 765 2,472 16,266 49, % 7 46,491 6,377 19,172 2,4J1 14,4 % AIwife888 14,51F E@:
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MILLIONS OF S D A A tJ C R $ . I I l' FIGURE 6- 16 rouv s:-A Ar AND MvNTstnN 0972; THE RICKER STOCK AND t o Art. 9 3 a c : A E P R E S E P. T Y E A * ' ' RECRUITMENT FUNCTION ESTiveTEs cr rirn Aevse.t,:t:
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. YEAR
{ FROM U S DEPART MENT or COVVERCE CURRENT riswERIE S STAti; TICS , TOTAL LANDINGS AND DOL.AR VALUE OF [ ACM ' YE AR'S CATCH) i E 1 FIGURE 6-17 MENHADEN LANDINGS FOR ALL MASSACHUSETTS PORTS
.h t
E 6.9 WINTs.R FIX>uNDr.R (Pseudopleurone ety americanus) The etfects of the operation of Pilgrim station Unit 1 and a Unita 1 and 2 combined have been assessed for winter flounder. g The winter flounder is a species of interest since it is a commerctally valuable resource and supports a recreational fiahery. Winter flounder in the area of Cape Cod hay exist in relatively localized populations. Howe et al (1976) summarize Perimutter N (1 % 7) as follove, "Following an early migration study, it was 5 postulated that each resident breeding population could be managea since young iish were the product of local spawning and adult movement.s were highly localized." The tagging study or
'I Howe and Coates (1975) in Cape Cod Bay, as well as other arean, indicates that 90 percent or the winter flounder tagged within an area were recaptured within the same area.
s The Plymout.h Harter-Kingston Duxbury Bay (PHKDB) area is the area i closest to the Pilgrim station where intensive breedire takes E 91 ace for winter flounder. Initially, a conservauve decision W was made to consider t.ne impact of Pilgrim station on the local
,, population. Localized populations are more sensitive to streuses I of the type which arise trom power station operation than widely dist.ributed populations.
. A further conservative assumption was made that the local l j.8 population is closed to migration from other populations . The result of this assumption was to concentrate the oftects of power stat. ion operation on the local populations ana not permit
['hu exchange with adjoining populations. entrained or impinged were assumed to be Thus, winter members or Ilounder the local population. Winter flounder populations exhibit a seasonal inshore-ot tahore uttgration within localized areas. The adulta move inshore to breed. The size of the breeding population can be estimat.ed at.
.. this time. An initial estimate of the size at the local population breeding in tha PHKDB was based on the size of the area and the breeding censities observed by Saila (1961). This I initial population size and distribution with age is presented in Table b-7.
The adults disperse to deeper water after the breeding season.
~I Winter flounder eggs are demersal or tend to be associa t.ea with the bottom. Thus, the eggs do not tend to be entrained. The
'g larvae are more plar.ktonic ano more apt to be suspended in the g water columru t.h e r e t o r e , they are transported by currents and dispersion. Since the population is localized, the larvae that survive remain in the area in sufficient numbers to repopulate I succeeding generations ot Ilouncer. Therefore, we have measured th e offeet of ent.rainment as being the reduction in larvae 6.9-1 I
remaining in the area, that is to say, the reduction in the E larvae which would be recruited into the local population. W 6.9.1 The Model 'Ih e winter flounder lire cycle model used f or this analysis was based on the model oeveloped by !!ess et al ( 19 "l 5 ) . A hicker stock and recruit. ment f unct.l on (see Section 6.6.1) wai parameterized by the method described by liesa et al (1975) . This tunction predicts the number of recruits in age-class 1 (R) trom the total number of eggs produced the previous year (L) : R (E) = E exp (-9 . 661- 1. 2 69x 10- 1 1 E) (6.9-)) This stock and recruitnvmt tunction is the only density-dependent component of the model. For egg densities in the population below 7.88 x 1011, a t. Increased number of eggs results in an a increased number or yearlings. For egg densities greater 7.98 x 1011, an increase in eggs results in a reduced number of than g yearlings per egg. The lite cycle of the winter flounder is assumed to have 12 age classes. The instantaneous natural nortality and Iishing . nortality rates for age-class 2 and older were assumed to be constant. Age-class 1 Ilsh were assumed to have no nortality EI W* from fishing and a natural mortality rate of 1.928 (Table b-7) . The yield to the commercial fishery was calculated by assuming a constant age-specitic weight from liess et al (1975) . The yield was calculateu in metric + ons using the fishing mortality and weights listed in Table b-7. (Also refer to Table b-6.) f The effect of the power plant on the winter flounder population was assessed ny sianulating the population for 40 years (plant g life expectancy) without any station-related erf ects, and taen W simulating the population with adjustments in mortality rates for entrainment and impingement. A sensitivity study has been conducted for the winter flounder lire cycle model. This study considered the ettects on the predictions of power station impact af ter 40 years of difierent values for f ecundity ano survivorship (S&W 1977). The dif f erent values for survivorship and f ecundity were based on a review of the published values of the parameters for winter flounder and g cover the range of plaustule values. m The sensitivity study concludes that the formulation in the g 316 Demonstration is the :rost conservative, leading to the g largest prediction of power station impact. E I 6.9-2 5 w
6.9.2 Lutroinment The effect of entr41 ament of winter founder larvae on the PimDB i population was characturited as an incr+itane in mortality to the larvan . An entimate or entrainment mortallt) w M derived trom a a mathematical modeling study conducted by the sti.f t ot the P.alph g M. Parsons Laboratory f or liater Reaouretsa and Hydrodynamics at KT. The M T study investigatec entrainment by enrpicying mathematical nodels to almulate circulation and diapersion of suspended turticles ai the water. 'niese nodels include the phenomena of I tides, currents, and winda to simulate t.hv transport of larvae during this planktonic life stage. circulation codel CAFE can be lound in Wang and Conner (1975) and A description of the a description of the dispersion model C10PER can be round in I Leinkuhler (1974). As an example ot the si.mulation of larvnl trannport, Figures b-18 ar.a 6-19 depict the center of mans Ior groups or larvae at various points of origin in the area of Pilgrim station. These '1 figures represent the o.trection in which the concentration of larvae would be transport.ed without regard to the dispersion of larvac irom the center at the mass. The I MIT study or larval en.rainment has been carried out in two phases. The first phase was conducted in 1975 and the resuits are reported un Pagenkopf et al (1976). In this study, 2 x 10' larvae were loaded into the PIEDB in two tidal cycles. The
!. larval production of 2 x 10' was determined trom breeding densities of winter flounder determined by Saila (19t31), the area ' of the PIEDb, the f acundity or winter flounder (11ess et al 1976), ; and the survivorship of eggs. The deciwion to compress the period of larval production into two tidal cycles was based on the extensive computer t ue required to perform a real time simulation and the linear nature at the problem.
Two sets of simulations were performed for this first phase. The rirst set estimated the transport of larvae without the ettect of I the Pilgrim station. This simulation providtM an idea of the number of larvae survivung and remaining in the P1mDb ar ea and
. consequently available for recruitment into the population as I juvenile winter flounder. Larvae are lost from the area due to death and transport out ot the area by physical pnenomena.
I The second set of simulations included the ef fects of Pilgrim station, Units 1 ana 2. by comparison of the number or larvae remaining in the popu.lation with aad without the offect of the in ta ke , an est nate of the 3.ncrease in larval nortality beyond I that normally experienceo was made. This mortality was estimated to be about 0.1 percent (0.001) . I b.9-3 2
This second simulation in the first phase also provided an est_truste of the tot.a1 numNr ut winter flounder larvae which passed through the intake. This number was compared to the number of larvae estimated to be produced in the PIDOB. The es ti. mat e indicated t. hat about 1 percent p . 01) of the larvae which ver e produced in the PIMDB passed through the intake of Units 1 and 1. This est.inste includes larvae which would have teen transported out of the ares and therefore lost to the populat. ion as well as larvae which would have died for biological E reasona. E A courpa rison of the two esti. mates provided an indication of the proportion of winter flounder larvae passing through the intake that would have been recruited into the juvenile population. While 1 percent of the larvae is entrained, the reduction in recruitment iu or'y 0.1 percent, since only 1 in 10 or the larvae ent. rained could have been recruited into the population . The remaining nine would have died or been transported away f rom the papulation regardless of thu presence of Pilgrim station. The original 316 Demonutration utilized the results or the first phase of the MIT study to estimate the effect of entrainment in the winter flounder lif e cycle nodel. The entrainment nortality of 0.001 (0.1 percent) reduction in recruit: tent was f actored into the life cycle model as an additional source of mortality. The result of the life cycle simulation was a 0.65 percent reduction in the size of the adult ilounder population atter 40 years of simulated power station operation for Pilgrim station Unita 1 and 2 (Table t>-8) . Subsequent to the original 31t> Demonstration and the rirst phase of the MIT stuay, hoston Edison contracted for field studies on winter flounder larvae in the PIEDB. These studies, conducted by Marine Research, Inc. during the 1976 spawing season tor winter flounder, provided real time estimates of the nu:nber of vtnter " flounder larvae in th9 P11KDb . 5 In 1977, MIT conducted the second phase of its modeling studf. - Th e results of this study are presented in Chau and Pearce (1977). The second phase had a primarf objective of verifylng the results or the first phase by making predictions s imilar ta the first phase but based on an input of field data. The second phase utilized the PIEDB field data collected by MRI to develop a rela time production of winter flounder larvae. The second phase, since it involved a real time simulation tor a period of aDout four months, was an exceedingly complex and lengthy simulation. Tne production of larvae determined by the MRI tield data, which g were used in the second phase of the MIT study, was 2.8 x 10e g_ larvae. This pas within an order of magnitude or the original production estimate developed f rom literature sources (2 x 109 larvae used an the first T has e of the MIT s tudy) , which is 6.9-4 5
E believed to be a reasonable agreement for the degree of uncertainty associated with t.he input parameters of the study. The second phase at the MIT modeling study utilizec a single set of simulations which included the ef fects of the Pilgrim intake. Based on this set of si;nulatione, the percentage of the larvae produced in the PIDWB which pass through the intake of Unit 1 was pro jected t.o be 0.8 percent and for Units 1 and 2 was projected to be 2.9 percent. The 2.9 percent agrees well with the comparable estimate I (2.7 percent) derived f rom the first phase of the MIT study for the northwest wind condition. Thus, the second phase does support the reasonableness of the estimates from the first phase. For the assessment of entrainment ef fects on winter flounder, the 316 Demonstration utilized the Southwest wind condition. This choice or southwest wind maximizes the estimate ot reductic,n in larval recruitment. (Table 1, Pagenkopf et c' 1976). The first phase of the MIT study concluded that, under the southwest wind condition, 1 in 10 of the larvae which pass through the intake would have been recruited into the PilhDB population. The results of the southwest wind condition yielded the largest estimate of recuetion in recruitInent of all the wind conditions. Therefore, this relationship was selected for application to the result.s of the 1977 study, and a reduction in I. recruitment of 0.08 percent was obtained for Unit 1 and 0.29 percent f or Units 1 and 2.
'n i 6.9.3 Impingement fg in addition to entrainment of larv u ,
population is also subject to impingement of adults, a ssumed to the winter flounder g , be age-class 2. The original estimate of mortality contained in the 316 Demonstration was made by crtrapolation trom Unit 1 I screenwashing data estimated 769 flounder would for 1974. be expression Ior impingement mortality rate is: For two-unit opera tion , an impinged per year. T:le M1 = -In (1 - No. impanged ) g No. 01 ago 2 tish (b .9-2)
'Ihis analysis assumes that all winter flounder impinged die and that all the impinged represent an increase in mortality to the local popula tion. Results of impos ing this additional I impingement mortality are prese'nted in Tsble 6-8.
the original coll ected . estimate, Impingement data for more recent 1972, impingement 1974, Subsequent to 1975, dau anct were 1976 I (Table 6-5) have been incorporated to give an average number of winter flounder impinged. The impingement mortality rigures and the results or imposing t.his additional mortality are given in Table 6-8. b.9-5 l
-. - . _ _ . .. .__- . ._ _ .. ~ . -.
6.9.4 Thenul Plume I me effect of the thermal dischstge can best be illustrated by the data gathered i.n -he
- field studies. Winter flouncer populations have been monitored preoperationall y and postoperationally in the vicinity of the thermal plume and at Warren Cove (control al a) . Figure 6-20 shows the locations of the trawl stations. Figure 6-21 shows the densities of winter flounder at both stations. In most cases, population density was g similar at both s ta tions , both preoperationally and 5 postoperationally. Reduction in the plume area population occurred in January 1974, which coincided with station shutduvn, g but reduction probably was the result of sampling variability as 5 it occurred briefly. In addition, the Warren Cove population was reduced in July and October of 1974 and, although the station was operating, there was no reduction in the vicinity of the plume, based on thermal tolerances given in Appendix A, winter flotu;Jer i will probably be excluded frora the area within the 100F isothenn E (about 7.4 acres) during summer months. Since the founder arc 5 bottom fish, and the plume will float, they will be able to avoid the area. should occur here. These entrained larvae have B already been accounted for in the entrainment impact estimates. g In the fall, adults will be excluded from about I acre in the lamediate area of the discharge.
6.9.5 Cumulative Impact Based on Unit 1 operating dati., the effect of the therm 11 plume on winter flounder is expected to be minimal. Yearly monitoring l4 a of trawl catches tar winte r flounder show no apparent station-related effects (aeo Figure 6-21) . , he eifects of entrainment and i.:rpinge: Pent combined are presented in Table 6-8. After 40 years of entrainment and impingement ., effects, a 3 percent reduction in population is expected as a result of Unit 1 operation, and a 7.3 percent reduction is I predicted as a result of Units 1 and 2 operation. Results f rom the 1977 MIT study are used for i.npact prediction since this g ent.rai.nment mortality was cased on field data as an input f rom g the studies in the local area. l The reduction of 7.3 percent over a 40-year period at power plant < l exploitation is believed to be a conservative estimate in that
- certain assumptions of this analysis tend to overestimate the effects of power station opera tion . Based on historical l
experience on the exploitation of fisherles, this exploitat ton appears to be at an acceptable level for the preservation of the integrity of the population.
's b.9-6 5
s 1 1.---. - - . _ _ _ _ . . . _ . _ _ _ __ _ _ _ . _ _ . , _ . _.. __ -. _
TABLE 6-7 PAPhiETEid OF Tile WINTER EOUNDER sit'ULATION MODELS Initial Instantaneous Intitantaneous Average Population Natural Fishing Weight AasMla ss Size Mortality Morta l it y (Grams) Fecundity 1 507,506 1.928 0.0 25.7 0 2 73,791 0.66 0.45 105.2 0 24,351 0.66 0.45 222.3 182,000 1 3 4 8,035 0.66 0.45 356.1 310,100 5 2,650 0.66 0.45 489.2 445,900 6 874 0.66 0.45 607.3 569,100 5 7 288 0.66 0.45 707.9 679,000 8 95 0.6b 0.45 793.7 774,900 g 9 32 0.66 0.45 861.4 8S1,900 3 10 11 0.66 0.45 913.9 910,700 11 3 0.66 0.45 954.2 956,900 12 1 0.66 0.45 988.3 996,000 617,637 5 1
.g \
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l Tid 3LE 6-8 RESULTS ur WINTr.R FLOLNUER SIMULATION OVDt A 40-YEAH PERIOD (basec on the accel of 11ess, Sinsenwine, and Saila 1975) Additional
. Forta lit y Population size L hutuction 1976 i ,Lunits 1 6 21 I lbn-affected population 0 610,030 0 Ent.rainment 0.001 606,890 0.65 (Phase 1, MIT study) 1x ingement 0.0104 N/5,330 5.81 (Dat.a f rom 1973-1974) -
c'. D1trainment and g Imp 2.ngement both 574,950 5.87 g (Phase 1, MIT study, data from 1975) 1977 l' lon-affocted
!. population 0 617,640 0 Entrainment (Phase II, MIT study) 8 Unit 1 0.0008 606,190 597,890 1.8 Units 1 6 2 0.00294 3.2 Impingement (Data avg . 1973-1976)
Unit 1 0.0026 600,610 2.8 Units 162 0.0076 583,710 5.5 D)traulment g (Phase II, MIT study) -E and Impingement (Data avg.)
' Unit 1 both 599,200 3.0 un 2 t.s 1&2 bo t.h 572,580 7.3 B ,m1
- I
I TABLE 6-9 SUl&JJiY OF ENTRAINMENT STUDY PILGRIM STATION - UNITS 1 AND 2 I PilASE I - MIT 1976 I 1. Percent- reduction in larval recruitment Plymouth Harbor- Kingston Duxbury Bay population due power station entrainment onlyt 0.1 percent. into the to
- 2. Percentage of larvae produced in Plymouth Harbor-Kingston Duxbury Bay which pass through the intake, including larvae which would have died from causes other than entrainmenti 1 percent PitASE II - MIT 1977
- 1. Percent reduction in larval recruitment into the plymouth Harbor- Kingston Duxbury Day population due to power station entrainment only: 0.29 percent
- 2. Percentage of larvae produced in Plymouth Harbor-
'a Kingston Duxbury Bay which pass through the intake,
'-g
. inclading larvae which would have died from causes other than entrainment: 2.9 percent t
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t l 6.10 POLLOCK (Pollachius virens) I Pollock is a predatory schooling fish species which is present at Pilgrim station during certain seasons of the year. could be subject to station impact through the thermal plume, Pollock entrainment of eggs and larvae, and impingement. The abundance of pollock in the vicinity of the station, measured The data I by gill net collections, is presented in Figure 6-22. were corrected for catch per unit effort. abundance is apparent. No decline in 6.10 .1 Thermal Plume There is little quantifiable evidence concerning the effect of
, 3 the thermal plume on pollock. Visual observations indicate that 5 pollock stay on the edge of the plume, feeding, and do not appear to be affected by the plume (R.B. Fairinnks , personal communication) . Thermal tolerance da ta I that pollock mortality could occur within the 200 isotherm (less than 1 acre) during the summer months.
(Appendix A) indicate Pollock avoid the immediate plume areas; thus, no nortality is expected.
- 6. 10.2 Entrainment
,h Pollock eggs and larvae are planktonic and therefore are subject 58 to entrainment. Eggs and larvae were collected during the entrainment monitoring study in 1974, 1975, and 1976. Because it !. g was difficult to dis tinguish pollock from other gadid and Ly glyptocephalus eggs, all these eggs were assun.ed to be pollock.
There was no such problem with larvae. These data were used to predict the impact of Units 1 and 2 on pollock. Assuming the number entrained is proportional to the volume of
. water withdrawn, the numbers of eggs and larvae entrained were i'-rl. predicted as though Unit 1 alone, and Units 1 and 2, had been operating in 1974, 1975, and 1976 (see Table 6-4) .
' g" The fecu.ndity of pollock has been reported as high as 4 million g- eggs per year per female (Bigelow and Schroeder 1953) with an average of 225,000 eggs per year per female. Age of first reproduction is 3 years and the life span rarely exceeds 10 years. Assuming 90 percent natural mortality from egg to I larvae, and using the equivalent adult model (described in Section 6.1) for entrainment due to Unit 1 alone, 498 adults may be lost because of 1974 operation, 353 due to 1975, and 63 due to E 1976 operation. It Units 1 and 2 had been operating during the same period, 1,b45 adults may have been lost due to operation in 1974, 1,168 due to operation in 1975, and 208 due to 1976 li operation.
6.10-1 I
6.10.3 I:ntrapment Pollock have been entrapped on the intake screens at Unit 1. Assuming the number entrapped is proportional to the volume of water withdrawn, the numbers of fish entrapped were predicted for l Unit 1 alone, and as though Units 1 and 2 had been operating full g time durlng 1973 through 1976. The results are presented in 4 Table 6-5. 6.10.4 Cumulative Impact No station impact on pollock from heat or cold shock is expected to occur through the thermal observations indicate that pollock position themselves outside the plume. Based on equivalent adult model estimates from plume because behavioral l entrainment and impingement predictions, between 208 and 3,165 5 adults could be lost to the population per year due to operation u of Units 1 and 2. The predictions are based on data collected from 1973 to 1976. An assessment of the impact on the total pollock population was made based on commercial harvest. Commercial fishing records give harvest estimates based only on eviscerated fish. The average annual harvest 11.7 million pounds. for Massachusetts Adult pollock potentially af fected by the (1970-1976) is l station were assumed to be equivalent to a 5-pound evis cerated E fish. Therefore, the potential station-related loss would W , represent from 0.009 to 0.135 percent of the Massachusetts commercial landings of pollock, and would therefore be negligible. I i-I I I I I 6.10-2 R
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I 6.11 CUNNER (Tautogolabrus adspersus) Cunner is an abundant local fish species found in the vicinity of Pilgri.m station. The relative abundance of cunner la s been increasing (Table 610) in the gill net catch, although there was I some population variability from month to month (Figure 6-2 2) due to variability in catch and movement offshore in winter. The sport fishing catch (Table 6-11) indicates the same trend as the catch with cunner predomitating in summer and f all . I gill net
'1h ere for e , cunner could expect to be moat operation in summer and fall. Canner affected by station could be af fected by the thermal plume, entrainment of eggs and larvae, and entrapnent.
6.11.1 Thermal Plume I Since the cunner population has been increasing both preoperationally and postoperationally, it appears that Unit 1 lu s had little offeet on the cunner populatien. Based on temperature tolerance data in Appendix A, the thermal plume for 3 I Units 1 and 2 should not result in overt nortality of cunner beyond the discharge canal. During y eriods of maximum ambient temperature (summer), cunner will probably not reside within the t 150 isotherm. Optimum spawning and adult growth should take place outside this area during the summer months. temperatures immediately outside the dis charge In the fall, canal will be optimal for growth. In spring, temperatures immediately outside the aircharge canal will be optimal for spawning and for the incubation and hatching of eggs. 6.11.2 En trainment Techniques ured for assessing tl'e impact of entrainment on the cunner population have been amended since the 19 % data were first evaluated. Due to the identification problems, all labrid and some early-stage limanda eggs were again assumed to be I cunner. A quantitative estimate of impact was deter nined f rom the percontage of the population potentially lost as a result of station operation; these percentages were taken f rom isocontours of larval loss as defined by a Massachusetts Institute of I Technology study by Pagenkopf et al (1976) . The first step in analyzing i:npact is to estimate the numtxtr of I larvae and the number of eggs in the impacted population. cunner eggs are buoyant and the larvae are planktonic, both are Since subject to entrainment by Pilgrim Station. As shown in Figure b23, an area of Cape Cod Bay around the plant was chosen for the evaluations. This area includes all shoreline for cunner spawning. The seaward I nearest to Pilgrim suitable boundary was arbitrerily chosen such that it includes only a part of the population. Assuming that the af f ected population is that of Cape Cod Bay, the area defined abave includes a subset of the I whole population ; looking at this subset as being the entire 6.11-1 I !
impactec population ir both practical and conservative since I impact is being imposed on A population smaller than that present g in the bay (thus impact is overestimated) . 3 Density samples were obtained during periods of egg and larval a occurence at stations located in the study area. An g approximation of the numbers of eggs (1.15 x 1011) and larvae (9.23 x 10') present was determined by multiplying the average density per cubic meter by the number of cubic meters in the area (dependent on the varying depth of Cape Cod Bay) . The percentage of eggs and larvae entruined is predicted by g knowing the manner in which Pilgrim Station acts as sink on the 3 egg and larval densities of Cape Cod Bay. From circulation and dispersion studies conducted by MIT, isocontours of percent , decrease in winter flounder larval concentrations resulting f rom station operation have been determined. These isocontours g (see Figure 6-23) were then applied to both the egg and larval populations of cunner since they represent a reasonable approximation of inpact for species such as cunner, which spawn along the shore. Thus, by calet'ating the equivalent number of eggs (1.09 x 10') and larvi (8.76 x 10 7) lost to entrainment, gl-the percentage of eggs and larvae entrained is determined: 3 g-8.76 x 10 7 x 100 2 1 percent of larvae entrained 9.23 x 10' i 1.09 x 10' x 100 1 percent of eggs entrained 1.15 x 1011 i The ef f ect of this additional 1 percent mortality sustained each year is best understood by use of the Leslie (1945) model as described by Horst ;1977) (also see Section 6-1) . This matrix == model predicts the finite population growth rate and stable age distribution which would develop under a schedule of age-apocific l fertility and survivorship. The finite growth rate, R. is represented mathematically by the maximum, positive real eigenvalue of the matrix. Parameters for the cunner ma trix are given in Table 6-12. Changes in any of the elements in die matrix, such as survivorship, necessarily result in change of the eigenvalue. Comparison of the original eigenvalue to that from the altered a ma trix , therefore, can indicate the significance of environmental impact on growth rate or age distribution. l An increased nortality of about 1 percent for both eggs and larvae is equivalent to an overall increase in mortality of about 1 percent to age class 0. Morta lity (0.01) is easily converted l to survivorship by subtra ction f rom 1 (=0. 9 9) . tie new E survivorshop of age 0 reflecting entrainment mortality is 5 6.11-2 R
=
I 0.199x103 Comparison of this eigenvalue to that of a non-impt.cted population shows that for every 1,000 individuals I produced originally, two will be lost to entrainment, an overall reduction of 0.2 percent per year. 6.11.3 Entrapment Numbers of adult cunner entrapped (see Table 6-5) on the intake screens at Unit 1 have ranged from a low of 87 in 1974 to a high of 2,299 in 1976; predicted entrapment for two-unit operation similarly ranges from 256 to 7,337, assuming the number impinged is proportional to flow. Assuming the worst - case entrapment of 7,337 fish for two-unit operation, this i.mpact wce avaluated in a manner similar to that l' for entrainme:x. Eige..v21ues from the cunner matrices with and without adjustment in survivorship for entrapment were compared. r. I Since no data wore available to describe the age class or classes subject to impingement, that age class was chosen where 3mpact to the overall population would be greatest, age class 4. The L additional mortality due to entrapment , 1.3435 x IO-r, was L determined by dividing the number of fish impinged (7,337) by the number of fish in age class 4 (extrapolated from the number of larvae and the survivorships of the previous age classes). The adjusted survivorship was calculated as: , (1 - mortality) x 0.6652 = 0.65627 (where 0.6652 is the survivorshop of age class 4). Comparison of the eigenvalues shows that for every 1,000 I individuals originally produced, two will be lost to entrapnent, an overall reduction of 0.? percent per year. { 6.11.4 Cumulative impact No mortality is anticipated due to thermal effects, although I during ra ximum ambient temparatures, cunner will probably not reside thin the 15 0F isotherr - Mortality from Units 1 and 2 is expF tet. 7nly as a result of entrainment and entrapment. The caaDined effects of entrainment and entrapment were assessed by eigenvalue analysis as previously described. Both sources of impact were simultaneously allowed for in the matrix and compared I to the non-impacted population; for every 1,000 individuals produced originally, 997 would be produced by the impacted population, an overall reduction of 0.3 percent per year. By way of comparison, the mxtality rate from sport fishing at Pilgrim is about 0.3 fish per hour during the six months of the year that cunner were caught in 1974 and 1975; the average
.I entrapment rate in 1976 is about 0.84 fish per hour. Considering 6.11-3 I
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_ 7 -, _ m M .m~ m M m m' W m' W W W W m M M W' TA122 6-11 S11MC FISal1NG CAlt 11 AT PIIERlH STATION, 1973-1975 April may . June July Aug 1974 1*+7 5 1974 1975 1974 1975 1973* 1974 1975 1971 1974 1975 On! 17 7 24 34 15 35 34 6 10 5 1 - Mackerel - - 2 - - - 46 - 42 5 - 18 Straped Ikass - - - 21 - 5 5 4 3 3 3 - Tautn3 - - 2 5 2 6 23 12 12 8 4 - IN211ock 208 - 90 25 95 122 461 25 24 41 8 11 Winter Flounder 60 - 70 23 70 30 35 26 45 2 6 17 Osnner - - 9 78 178 542 82 240 999 - 157 316 B uncami - - - 3 2 - 11 - - - - - Aumrican Eel - - - - 4 - - - 3 - - - isluet ish - 2 4 8 15 62 68 92
" Snapper" tiluetish - - - - - - - - - -
1,0H6 47 Sept. Oct ta sy Totals
- 1973 1974 1975 1973 1')74 1975 1973 1974 1975 1973 1974 1975 Gad - - -
15 72 - - 4 - 59 1.19 86 Mtekerel -- - - - - - - - - 51 2 60 Striped tlass 127 - en $11 32 - 2 - - 648 39 35 Tautx>g 14 4 5 24 4 3 - - - 69 28 31 Pollock 11 4 4 75 10 - - - -
- 28 8 440 186 Winter Flounder - - - - - - - - -
37 232 115 Cunner - 466 128 - 244 40 - - - 82 4,294 1,087 Tumcod - 4 - 2 1 - - - - 13 7 3 Ainerican Eel - - - - - - - - - - 4 3 111ue t i sh 441 615 14 127 69 - - - - 634 760 123
" Snapper" ill uet ish - 140 180 - - - - - -
- 1,176 277
- 1973 survey cxm:nenced in July i
1 of 1
M M 'M M M U' M M M M M' M' M M .M M M M TAMI.F. 6-12 ESTINATiuN OF AGE-SPECIFIC FERTILITY AND SURVIVAL FUH CUNNER Nesmiser 8
- 9 &andwert F 8 Age -a LengtM 83 heagtst # 3 3 Fert.a lit y s s ) Dyls/Adul tt S D of fish of fish
_{ yea r s}_ tass) b r_a_u i Je*14 S/lembe lel Sex r.at io(
- 3 1, Col lect e<f l>s etlic-t ed E O O 0.0002101**8 1 46 1.34 268 0.317 85 71 73.1 0.6252 2 89 11.00 2,201 0.317 698 lb 45.7 0.6252 3 12 4 32.0 1 6,402 0.317 2,029 35 2H.6 0.6252 4 15 3 e5.58. 12,515 0.317 3,967 il 17.9 0.6252 5 177 99.28 19,856' O.317 - 6,294 22 11.2 0.62?>2 h 1% 138.74 27,743 0.317 u,7% 3 1.0 0.62"2 7 212 17H.27 35,655 0.317 11,301 0 4.4 0 as) L = 284.77 (1-Exg( -0.1979 (i-0.104 4 ) j) from Sercisuk (1972 Table 7)
(28 LcwJ h; = -5.2216
- 3.21214 (log ly ) , from serchuk (1972, Taule 8)
(88 Assum+si 1ine.sr rel at_ionship bet. ween weight and iert ilit y (1Legena 1 1967) 200 t ggs/9ra isply weight irima Williams et. 41 (197_l, p. 189) (*8 Prop 3rtson of time guig>ulat iosa vis tess is female f r om Dew (1970, p. 21) 8*8 Eggs / adult is eggs /temale t isses the pro:w t ion of time g=>gsulat. ion which is tesale aa; From Serchuk (1972, Table 31 (FD Based on regression of number of fash collectest (n) against age (i) ,- In (h)
- 4.76 - 0.469hi, r = -0.82 S,, = 0.55 -
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I 6.12 RAINBOW SMELT (Osmerus mordax) I The eff ect of the operation of Pilgrim Units 1 and 2 on the smelt population in the area is predicted from published life history information and plant monitoring data . The sources of impact to the population include entrainment of larvae and impingement of I adults. The maximum temperature predicted in the intnediate area of the discharge during the summer is near the upper maximum temperature tolerance presented in Appendix A for smelt. It is s therefore assumed that adult smelt will be excluded from the immediate area of discharge. From the combination of the area of exclusion and the mobility of the adults, this source of impact is judged to be negligible and will not be quantified in the present analysis. Marine populations of this species generally spawn upstream of the tidal influence and the eggs are adhesive. While there is a net downstream movement of larvae, McKenzie (1964) reports that larvae are carried back and forth under the influence of the I tide. After a few days, the larvae become negatively phototropic which results in higher densities near the bottom during the day. It may be concluded from this strategy that larvae are retained u in the brackish estuary and those which are washed out of the estuary have a lower probability of being recruited into the
', adult population.
Refer to Section 6.9 for a discussion of the ef fect of the Pilgrim Station on populations in the Plymouth-Duxbury Harbor. 3 The analysis presented in Section 6.9 is for winter flounder; f towever , the etfect on the larval smelt population would be i similar, since both populations breed in the Plymouth-Duxbury
?1 area. Smelt breed in the rivers while flounder breed closer to ,. the mouth of the estuary; therefore, the predictions for winter flounder larvae entrainment will be overestimates for smelt.
6.12.1 The Model Presently, there is no published population dynamics lif e cycle model for smelt. A paper by McKenzie (1964) was used to obtain I statistics for the development of a life table for use in the present analysis. While the statistics were gathered for the smelt population of the Miramichi River in New Brunswick, comparison with the work of Warfel, Prost, and Jones (1943) in Great Bay, New Hampshire, and Rothschild (1961) in Dean Brook, Maine suggests that the values are applicable to other populations. It is therefore assumed that this life table is
-I applicable to the population which could be af fected by Pilgrim Station.
o The life table for smelt is presented in Table 6-13. The survivorship f or ages 2 through 5 and the estimates f or f ecundity
)- were taken from Mckenzie (1964) . The survivorship for age 1 was assumed to be the same as for larvae to age 1 and the
~ 6.12-1 I
survivorahip for age 6 was assumed to be the same as age 5. The number of eggs produced by fish from ages 2 to 5 was calculated using the McKenzie (1964) estimates of fecundity. A function for egg survivorship was developed from McKenzie's data by polynott.ial regression. L = -3588 + 1191 (E) -124 (E) 2 + 4 . 2 (E) 3 [ F = 7.789, a 50.05) r L is larval density per ft2 of surf ace area, and 3 E is the natural log egg density per ft2 of surface area. E The estimate of fishing mortality was taken from the Miramichi smelt fishery since no other estimate was available. This fishery uses trap nets. McKenzie (1964) estimated a 4 percent annual harvest for ages 2 through 4. Therefore, a fishing mortality of 0.04 per year was used in the simulation. An estimate of the density of smelt in the Plymouth-Duxbury Harbor was made from data collected by the Massachusetts Division g of Marine Fisheries in 1971. Smelt were collected in a 30-foot 3 shrimp trawl in 5-minute tows at 1 to 2 knots. The area swept by this trawl was estimated to be approximately 1,411 m a. Sr;elt were most consistently collected during November when an average ; of 10.33 individuals (standard error of 2.84) was collected per trawl. It was assumed that this trawl had an efficiency of 50 percent - and, on the average, it sampled no more than one-half of the water column. It is also assumed that the adult smelt have a 3~ uniform distribution with depth. This yields an estimated 3 density of adults in the harbor of 0.0027 per ft2 of surface area. um
'Ihe density of eggs in the Jones River, where the Massachusetts l
Department of Marine Fisheries collects smelt eggs, has been estimated as high as 230,400 per square foot during each period of collectilon (pers. comm. , B. DiCarlo). It was assumed for conservatism that the average density of eggs was about 1,000 eggs per square foot over the area b which spawning takes place. The number of eggs produced each season (E) can be estimated: E = X.R.T ( 6 .12 - 1) where X is the standing crop of eggs per square foot, R is the area of the river which eggs are deposited, and 6.12-2
= .
I T is tha turnover rato for cgga. me adult population (A) which resides in the harbor during the fall is: A = Y.H (6.12-2) where Y is the standing crop of adults per square foot, and 8 H is the area of the harbor. We turnover rate for adults is asfumed to be one. The L relationship between the nu:xtber of eggs (E) and adults (A) in the population is: E = A.F.S (6.12-3) where F is the fecundity, and S is the sex ratio. Substituting Equation 6.12-2 into 6.12-3, and setting this equal
., Equation 6.12-1:
F.Y.H.S = X.R.T. (6 .12-4 ) Equation 6.12-4 cz.n be solved for the turnover rate T: T=,H . F.Y.S ( 6 .12-5) R X Estimates of the adult density Y and the egg density have been made. The average fecundity from Table f>-13 is 15,560; the adult
, , density is 2 x 10-3; and the egg density is 103 per square foot.
3- ne turnover rate becom.is: og T= H . 1.5 x 10
- x 2 x 10-3 7 = H . 2.1 x 10-2 H 10-2 R 103 R R I The estimate of the number of eggs in the population becomes:
En X . R .T=X.R. H . 10-2 =X .H. 10-r ( 6 .12-6 ) R has been estimated as 1.95 x 107 I The area of the harbor square meters at mean low water. is estimated as: (H) Therefore, the number of eggs E=X . H . 10-2 = 103 . 1. 9 5 x 10 7 . 10.764 . 10-2 = 2 x 10' 6.12-3 I
The initial population structure and the equilibrium population I structure for the simulation are presented in Table 6-14. The 3 estimate of the number of larvae entrained results from an B extrapolation from the densities of smelt entrained at Unit 1. _ Basad on these densities and the combined flows of both units, an average value of 3.1 x 106 larvae for Unit 1 alone and
- 1. 0 x 10 7 larvae for Units 1 and 2 would be entrained per year.
It is conservatively assumed that the number of adults potentially recruited from this number of larvae were lost to the population. The number of smelt impinged each year was estimated from the E Unit 1 screenwashing data from 1973 to 1976. The extrapolation E for twc-unit operation assumes the fish are impinged in proportion to the flow. It was estimated that an average of M 768 smelt for Unit 1 alone and 2,909 smelt for Units 1 and 2 l would be impinged per year. It is assumed that all thes e fish are of age 2. 6.12.2 Cumulative Impact The effect of this loss of young fish on the adult population was (. i.nvestigated by adding the mortality attributable to entrainment I and impingement to the simulated population. The effect of the thermal plume was not considered in this analysis due to the ; negligible nature of the effect. 1 The population was resimulated, including the mortalities associated with power station operation. The population size was depressed by 1.15 percent for Unit 1 alone, and 3.74 percent for Units 1 and 2, when compared to the non-impacted population af ter 40 years. The impacted population came to equilibrium as did the l non-i.mpacted population. m' as I I I I I 6.12-4 i E
TABLE 6-13
. LIFE TABLE FOR SMELT Sex Ratio lae _ Survivorship Fecundity (Female / Male) Weight (grams) -I Eggs 0.036 0 I Larvae 1
2 0.070 0.070 0.454 0 0 11,488 0.23 8 14
.3 3 0.133 22,847- 0.23 17 3 4 0.094 33,120 0.25 22 , 5 0.072 45,555 0.24 32 6 0.072 59,980 0.50 9
I Lg I 13 LJg I I
.I 1 of 1 I
I TABLE 6-14 INITJ.AL AND EQUILIBRIUM POPt.TLATION STRUCTURES FOR SMELT SIMULATION Initial Equilibrium Age Number thmber
,j i.
's Eggs 2 x 10' 7.355 x 10' Larvae 7.19 6 x 10 7 2.647 x 10s I 2 3
1 5.066 x 106 3.567 x 10s 1.621 x 10 s 1.863 1.312 5.962 x x x 107 106 105 4 2.161 x 10 4 7.947 x 10* -I 5 2.034 x 103 7.479 x 103 6 1.47 x 102 5,41 x 102 s. I in 11 r. -r . L y, I
.I:
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j 6.13 ATIANTIC SIINERSIDE (Menidia menidia) The inpact of operation of Pilgrim Units 1 and 2 on silversides is predicted from temperature tolerance data, entrainment data,
" and screenwashing data. Published life history data on silversides were researched to obtain fecundity, sex ratio, and life span.
6.13.1 Results of Thermal Plume, Entrainment, and Impingement Temperature tolerance and acclimation information is presented in Appendix A. Based on these data, silversides can be anticipated to be excluded from about 7.4 acres inside the 100F isotherm area during the summer. It is expected that many of the fish will
' simply move to other areas to avoid the thermal plume. The effect of this impact will not be quantified in the present analysis.
Larval silversides were collected in entrainment studies from
- 1974 to 1976 (see Figure 6-24) ; eggs were found entrained in 1975
;- and 1976. Integrating over the density curve of eggs and larvae collected (see Table 6-4) provides an estimate of entrainment for two-unit operation. The equivalent number of adul cs was 'L estimated.by assuming the fecundity is 300 egge per female, and 'g that 1 in 10 eggs hatch (Bayliff 1950).
Using the formulas: [* No. adults lost = no. larvae entrained x 2/F.E and
, No. adults lost = (no, larvae entrained x 2/F.E) + (no. eggs entrained x 2/F) where F = fecundity and E survivorship of eggs to larvae; between 21, 587 and 187,267 adults per year are predicted lost as
= a result of two-unit operation.
- h "E
Assuming an adult silverside weighs aboat 10 grams (Austin et al 1973), the loss of this many adults would be equivalent to a loss r of between 476 and 4,128 pounds per year.
. The loss due to i.npingement has been estimated from data callected in impingement monitoring programs from 1973-1a76 (see Table 6-5) . The predicted loss for both Units 1 and 2 is between approximately 2,392 and 2,820 fish per year. Assuming again that these fish weigh 10 grams each, this results in a loss of 53 to 62 pounds per year.
I The to combined effect of entrainment and impingement is predicted be 23,980 to 190,000 fish per year, or about 529 to 4,191 pounds per year. Since this species is not of commercial
- I value in Massachusetts, no comparisons with commercial catch in Massachusetts can be made. Anderson and Power (1950) reported
,I 6.13-1 d
l that 126,300 pounds of silversides were commercially caught in l New York State in 1946. The availability of silversides may also be indexed by the number caught in seines. Bigelow and Schroeder (1953) reported that up to 3,500 were caught in a single seine gl haul from the southern side of the Gulf of St. Lawrence. Warfel 5 and Merriman (1944) reported as many as 1,938 in a 30-f oot seine which was fished for about 100 feet parallel to shore in water less than 4 feet deep. 6.13.2 Cumulative Impact The effect of the thermal plume is exoected to be minimal to silversides based on the abundant nature of the species and the area from which they could potentially be excluded (7.4 acres). No observation of thermal impact to silversides has occurred. An estimated 23,900 to 190,000 adults could be lost from entrainment and impingement combined. These losses assume no compensatory a mechanism in the population and are therefore an overestimate of g the impact to this species. The abundant nature of this species would suggest a minimal impact to the population from this additional source of mortality. I I I I I I I I I 6.13-2 I ' B
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LARVAE OBSERVED AT UNIT l 1974 THROUGH 1976 g I
I 6.14 ALEWIFE (Alosa pseudoharengas) The impact of the operation of Pilgrim Nuclear Power Station, Unit s 1 and 2, is predicted from published life history informa tion and station operation data. The sources of possible I. impact from station operation include the thermal plume, entrainment of larvae, and mortality of adults on the traveling screens. 6.14.1 Results of Thermal Plume, Entrainment, and Impingement Based on the studies presented in Appendix A, and the predicted areas of various isotherms in Section 2 of the July 1975 report, it is predicted that alewives will be excluded f rom about 2 acres in the imnediate area of the discharge. The studies of Stanley and Colby (1971) indicate that alewives are able to tolerate temperatures up to 87.80F, which is near the predicted summer maximum surf ace temperature at the discharge area. Based on avoidance temperatures (see Appendix A), it is anticipated that most alewives will avoid the thermal plume. Since this should not constitute a problem, it will not be quantitatively considered in the present analycis. Calculation of entrainment impact was made by assuming the a everage fecundity i.s 229,000, the sex ratio is 1 to 1 (Kissil 1974), alewives reproduce three times in their life (Marcy 196 9) , and the survival of eggs is no less than 1 in 10 (Edsall 1970) . For further details on lif e history infor nation, see Section 5.13 of the original report. The number of larvae predicted to be entrained with two units operating at the Pilgrim site was based on Unit 1 entrainment studies conducted from 1974 to 1976. During this 3-year period, very few alewife larvae were entrained; the largest entrainment predicted for two-unit operation of 9.57 x 105 larvae occurred in 1974, and the low of no larvae entrained occurred in 1975 (see Intermediate numbers of larvae were entrained during h3 Table 6-4). 1976. Tne number of adults expected to survive from this number of larvae had they not been entrained varied f rom zero to about 28 adults for 1975 and 1974 respectively (see Figure 6-25) . Extrapolation of larvae lost through entrainment to adults lost , is made using the method outlined in Section 6.1. Using the greatest entrainment value, the largest number of adults predicted lost is: Na*S 1N1 = 9.57 x 105 x 2/(3 x 229,000 x 0.1) = 28 adults /yr . The losses due to impingement are predicted f rom data collected g in the Unit 1 impingement monitoring programs of 1973 to 1976. E Since the fish collected in these programs are small, they are identified only as clupeids. As with other clupeids considored I 6.14-1 I _ -- t
(. _.__ .. I in this report, it is conservatively assumed that all clupeids impinged are alewives. The predicted number impinged each year is between 14,450 and 48,557. The combined effects of impingement and entrainment should be less than 50,000 fish per year for two-unit operation. This ' analysis assumes no compensatory mechanisms in the population which would be reduced by this number. The analysis also does not consider species other than alewives collected in the clupeid category in the screenwashing programs. To give some perspective to this number of fish, Kissil (1974) 3 reported 184,151 and 14 0,203 (162,177 average) alewives in Bride } Lake,~ Connecticut, which has an area of 18.2 hectares. If the same breeding density were to occur in the areas near the Pilgrim station, this would be equivalent to removing spawning adults from 5.61 hectares, or 13.86 acres. The weight of adult alewives can be roughly calculated at about one--half pound . Bigelow and Schroeder (1953) reported that 526,500 fish were caught in Cape Cod Bay and the Merrimack River g in 1896, having a total weight of 293,671 pounds. This is about E 0.56 pound per fish. Using this average weight, the 50,000 fish would weigh 29,000 pounds. This would have been 9 percent of the 1896 catch. Unfortunately, no recent catch statistics for the local alewife fishery are known to exist. 5.14.2 Cumulative I:apact , The effect of the thermal plume is expected to be minimal . Allowing for no compensation by the population, no more than appoximately 28 and 50,000 adults are er:pected lost due to - entrainment and impingement, respectively. The effeet of this additional nortality on the popula tion is expected to be minimal. - s I I I I 6.14-2 5 m
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T 3 I NOTE NONE ENTR AINED IN 1975 FIGURE 6-25 DENSITY OF ALOSA SPP. LARVAE OBSERVED AT UNIT I I 1974 THROUGH 1976
I 6.15 REFERENCES References for 6.1 Leslie, P.H. 1945. On the Use of Matrices in Certain Population Ma thematics . Biometrika, 33:183-212. I Reinsch, J.W., and Wilkinson, J. 1971. Computations, Volume I: Berlin. Linear Algebra. Handbook for Automatic Springer Verlag.,
. References for 6.2 (Irish Moss)
Clapp Laboratories, Battelle Memorial Institute. 1971-1974 (Benthic Studies) . See Appendix B. i mrine Research, T.n c . 1973. (Entrainment Studies) . See
. Appendix B.
mas. Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of m rine Fisheries, 1968-1977. (Marine Ecology Surveys). See Appendix B. Michael, A., Dr. and Wilce, R.D., Dr. 1974-1977. (Benthic Studies) . See Appendix B. i Prince, J .S . 1971. An Ecological Study of the Marine Red Algae Chondrus crispus in the Waters of Plymouth, Mass. Ph.D. Thesis, Cornell University, New York. I jg Ryther, J.H.; Gifford, C.E.; Lapointe, B.E.; and Clifford, C.H. E 1974-1976. Woods Hole Oceanographic Institution (Irish Moss Quality Surveys) . See Appendix D. References for 6.3 (Rockweed) Clapp Laboratories, Battelle Memorial Institute. 1971-1974. (Benthic Studies) . See Appendix B. Fritsch, F.E. 1945. The Structure and Reproduction of the Algae, Volume III. Cambridge [ England ) at the University Press . Wilce, R.D., Dr. 1974-1977. (Benthic Studies) . See Appendix B. R_eferences for 6.4 (Amphipod) Clapp Laboratories, Battelle Memorial Institute. 1971-1974. (Benthic Studies) . See Appendix B. Sameoto, D.D. 1969. Physiological Tolerances and Behavior Responses of Five Species of Haustoridae (Amphipoda: Crustacea) to Five Environment Factors. Jour. Fish Res. Bd. Can. 26 (9) : 2283-2298. I 6.15-1
I e l' Richael A. Dr . , and Wilce, R.D., Dr. 1974-1977. (Benthic - Studies). See Appendix B. - References for 6.5 (American Lobster) Beals et al. 1970-1974. Massachusetts Coastal Lobster Fishery Statistics. Division of Marine Fisheries, Massachusetts Department of Natural hesources. Hughes, J.T.; Sullivan, J.J.; and Shleser, R. 1972. Enhancement E of Lobster Growth. Science, 177:1110-1111. E Marine Research, Inc. 1974-1976. (Entrainment Studies of Lobster La rvae) . See Appendix B. Mass. Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of Marine Fisheries. 1968-1977. (Marine Ecology Surveys). See Appendix B. Morrissey, J.D. 1971. Movements of Tagged American Lobsters, g Homarus americanus, Liberated of f Cape Cod, Mass. Trans. Amer. Ec Fish. Soc. No. 1. Saila, S.B.; Flowers, J.M.; and Hughes, J.T. 1969. Fecundity of Americar. Lobster, ,Homarus americanus. Trans. Am. Fish. Soc. No. 3:537-539. References for 6.6 (Mussel) Clapp Labora tories , Battelle Memorial Institute, 1971-1974 l (Benthic Studies) . See Appendix B. 5 Marine Research, Inc. 197 3- 19,77 . (Entrainment Studies) . See " Appendix B. l, Michael, A., Dr. and Wilce, R .D . , Dr. 1974-1977. (Benthic Studies). See Appendix B. Purchon, R.D. 1968. The Biology of the Mollusca. Pergamon Press, London. Pear ce , J.B. 1969. Thermal Addition and the Benthos, Cape Cod Canal . Ches . Sci. 10 (354) :230-231. References for 6.7 (Common Perivinkle) Clapp Laboratories , Battelle Memorial Institute. 1971-1974. (Benthic Studies) . See Appendix B. Furine Research, Inc. 1973-1977. (Entrainment Studies) . See l Appendix B. m I t 6.15-2 5 5 1
I I Michael, Studies). A., Dr. and Wilce, See Appendix B. R.D., Dr. 1974-1977. (Benthic: Newell, R.C.; Pye, V.I.; and Absanullah, M. 1971. The Effect of Thermal Acclimation on the Heat Tolerance of the Intertidal Prosobranchs Littorina littorea (L) and MondOnta lin ea ta (DaCosta) . J. Exp. Biol. 54: 525-533. Purchon, R.D. 1968. The Biology of the Mollusca. Pergamon Press, London. References for 6.8 (Atlantic Menhaden) Barker, A.; Testaverde, S.; Marcello, R.; and McLeod, JW Clay, A.; G.C. 1974. Observations on the Effects of Gas Embolism in Captured Adult Menhaden. Presented at: Battelle Northwest
> Iaboratories and U.S. Atomic Energy Commission Gas Bubble Disease d
Workshop, October 8-9, 1974, Richland, Washington. s DeMont, D.J., and Miller, R.W. 1971 First Reported Incident of g Gas Bubble Disease in the Heated Effp ent of a Steam Generating Station. Proc. 25th Ann. Conf. S.E. Assoc. Game and Fish Comm. ' j'E Higham, J.R., and Nickolson, W.R. 1964. Sexual Maturation and E Spawning of Atlantic Menhaden. Fish. Bull. 63 (2) : 255-271. Lg Marcello, R.A., and Fairbanks, R . B ., 1974. Gas Bubble Disease "E Mortality of Atlantic Menhaden, Brevoortia. tyrannus, at a Coastal Nuclear Power Plant. Presented at: Battelte Northwest i Laboratories and U.S. Atomic Energy Commissich Gas Bubble Disease j Workshop, October 9-9, 1974, Richland, Washington. I'. Marine Research, Inc. 1973-1977. (Entrainment Studies). See l Appendix B. Marine Research Institute. 1976-1977. (Impingement Study) . See Appendix B. i. Mass. Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of Marine Fisheries. 1976-1977. (Screenwash monitoring for
. impingement) . See Appendix B.
Reintjes, J.W. 1969. Synopsis of Biological Data on the Atlantic
'~
Menhaden, Brevoortia tyrannus. U.S. Fish Wild 1. Serv., Cire. 320. I Ricker, W.E. 1958. Handbook Statistics of Fish Populations. of Calculation for Biological Fish. Res.~Bd. Can. Bull. 19. Schaaf, W.E., and Huntsman, G.R. 1972. Ef f ects of Fishing on the Atlantic Menhaden Stock: 1955-1969. Trans. Amer. Fish. Soc. 101:290-297. I 6.15-3 I
References for 6.9 (Winter Flounder) Chau, T.S., and Pearce, B.R. 1977. Simulation of Larvae Dispersion and Entrainment near a Coastal Power Station, Ralph M. Parsons Laboratory, Dept. of Civil Engineering, MIT. Hess, K.W.; Sissenwine , M.P. ; and Saila, S.B. 1975. Simulating g the Impact of the Entrainment of Winter Flounder Larvae, pp. 1-29 3 in: Saila, S.B. (ed.) . Fisheries and Energy Production: a Symposium. D.C. Heath & Co. , Lexington, Mass. . Howe, A.B., and Coates, P.G. 1975. Winter Flounder Movements, Growth and Mortality off Massachusetts. Trans. Amer. Fish Soc. 104 (1) ; 13-29. Howe, A.B.; Coates, P.G.; and Pierce, D.E. 1976. Winter Flounder Estuarine Year-Class Abundance, Mortality, and Recruitmeat. 3 Trans. Amer. Fish Soc. 10S (6) ; 647-657. E Leimkuhler, W.F. 1974. A Two-Dimensional Finite Element g Dispersion Model. Thesis, Dept. of Civil Engineering, MIT. 5 Marine Research, Inc. 1974-1976. (Ichthyoplankton Survey of Cape Cod Bay). See Appendix B. { Marine Research, Inc. 1973-1977. (Entrainment Studies). See - Appendix B. { Parine Research, Inc. 1976-1977. (Winter Flounder Larvae Studies). See Appendix B. I t Marine Research Institute. 1976-1977. (Impingement Study). See Appendix B. ,, Ma ss . Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of Marine Fisheries. 1973-1975. (Screenwash monitoring for impingement) . See Appendix B. Mass. Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of Marine Fisheries, 1968-1977. (Marine Ecology Surveys). 3 See Appendix B. 3 Pagenkopf , J.R.; Christodoulou, G. C.; and Pearce, S.R. 1976. Circulation and Dispersion Studies at the Pilgrim Nuclear Power ' Station, Rocky Point , Mass., Ralph M. Parsons Laboratory, Dept. of Civil Engineering, MIT. 3311a c S.B. 1961. The Contribution of Estuaries to the Of fshore Winter Tounder Fisheries in Rhode Island. Gulf and Caribbean Fimberies, Inst. Proceedings luth Annual Session, November 1961, pp ., 95-109. E E r 6.15-4 5
=,
lI I Stone & Webster Engineering Corp. 1977. Sensitivity Analyses on Winter Flounder Life Cycle Model Using Different Mortality and Fecundity Estimates. Submitted to Region I, U.S.E.P.A. by Boston Edison Company , March 1, 1977. Wang, J.D., and Connor, J.J. 1975. Mathematical Modeling of Near Coastal Circulation . Report No. 200, Ralph M. Parsons I Laboratory, Dept. of Civil Engineering, MIT. References for 6.10 (Pollock) I Bigelow, H.B., Maine. U.S. Fish and Wildlife Service, Fish and Schroeder, W.C. 1953. Fishes cf the Gulf of Bulletin 74, Vol. 53, 1953. Marine Research, Inc., 1973-1977. (Entrainment Studies). See g Appendix B. ig Marine Research Institute. 1976-1977. (Impingement Study) . See Appendix B. Mass. Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of Marine Fisheries. 1968-1977. (Marine Ecology Surveys). See Appendix B. .. Mass. Dept. of Fisheries, Wildlife and Recreational Vehicles, l Div. of Marine Fisheries. 1973-1975. (Screenwash monitoring for
< impingement) . See Appendix 3.
References for 6.11 (Cunner) I Bagenal, T.B. 1967. A Short Review of Fish Fecundity. pp. 89-11 Gerking, S.D. 1967. The Biological Basis of In: (ed . ) Freshwater Fish Production: A Symposium sponsored by Sectional 1 Committee on Productivity of Freshwater Communities of the International Biological Programme. Blackwell Scientific Publications , Oxford, England. Dew, C.B. 1970. A Contribution to the Life History of the Cunner, Tautocolabrus adspersus (Wa lbaum) , in Fisher's Island
, Sound. M.S. Thesis, Univ. of Connecticut, Storrs, Conn.
Horst, T.J. 1977. Use of the Leslie Matrix for Assessing I Environmental Impact with an Example for Fish Population. Trans. Am. Fish. Soc. 106(3) . Leslie, P.H. 1945. On the Use of Matrices in Certain Population Mathematics . Biometricka. 33:183-212. Marine Research, Inc. 1973-1977. (Entrainment Studies). See Appendix B. 6.15-5 I '
l 1 I thrine Research Institute. 1976-1977. (Impingement Study) . See Appendix B. Pa ss . Dept. of Fisheries, Wildlife and Recreational Vehicles, E Div. of Marine Fisheries. 1968-1977. (Marine Scology Surveys) . 5 See Appendix B. Mass. Dept. of Fisheries. Wildlife and Recreational Vehicles, Div. of Parine Fisha, ries. 1973-1975. (Screenwash monitoring for impingement) . See Appendix B. Pagenkopf, J.F . ; Christodoulou, G.C.; and Pearce, B.R. 1976. Circidation and Dispersion Studies at the Pilgrim Nuclear Power Station, Rocky Point, Mass., Ralph M. Parsons Laborator'f, De,t E of Civil Engineering, MIT. 5 Serchuk, F.M. 1972. The Ecology of the Cunner, Tautocolabrus_ g adspersus (Walbaum) (Pisces: Labridae) , in the Weweantic River Estuary, Wareham, Massachusetts. [ ft . S . Thesis, University of Massachusetts, Amherst. Vaughan D.S., and Saila, S.B. 1976. A Method for Determining Mortality Rate Using the Leslie Mstrix. T"ans. Am. Fish Soc. ' 10 5: 380-383. Williams, G.C.; Williams, D.C.; and Miller, A.J. 1972. Mortality Rates of Planktonic Eggs of the Cunner, Tautocolabrus adspersus 3 (Walbaum) , in Long Island Sound. In: Pacheco, A.L. (ed) . [ Proceedings of a Workshop on Egg, Larval and Juvenile Stages of Fish in' Atlantic Coast F.stuaries. Nat. Mar. Fish. Serv., Middle Atlantic Coastal Fisheries Center, Tech. Puh. 1. References for 6.12 (Smelt) , McKenzie, R .A . 1964. Smelt Life History and Fishery *.n the Miramichi River, New Brunswick. Fish Res. Board, Canada. Bull No. 144 Marine Fesearch, Inc. 1973-1977. (Entrainment Studies). Sec Appendix B. Marine Research Institute. Appendix B. 1976-1977. (Impingement Study). See I Mass. Dept. of Fisheries, Wildlif e, and Recreational Vehicles, Div. of Marine Fisheries. 1976-1977 (Screenwash monitoring for impingement) . See Appendix 3. Rothschild, B .J . 1961. Produc. tion and Survival of Eggs of the American smelt osmerus mordax (Mitchill) in Maine. Trans. Amer. Fish Soc. 90: 42-48. 6.15-6 E;i; m ,'
t* I Warfel, H.E.; Frost, T.P.; and Jones, W.H. 1943. The Smelt Osmerus mardax in Great Bay, New Hampshire. Trans. Amer. Fish Soc. 72: 257-262.
.I References for 6.13 (Atlantic Silverside)
-M Andernou, A.4 . and Power, E.A. 1950. Fishery Statistics of the E United States , 1946. U.S. Fish Wildl. Service, Statistical Digest 19, p. 118.
Austin, H.M.; Dickinson, J.; and Hickey, C. 1973. An Ecological Study of the Ichthyof auna at the Northport Power Station, Long Island, New York. Long Island Lighting Company. i ' Bayliff, W.H. 1990. Ti m fe History of the Silverside, Menidia
,menidia, Chesapeake Biological Laborator'/. Publ. No. 90.
' Bigelow, H.B., and Schroeder, W.C. 1953. Fishes of the Gulf of Maine. U.S. Fish and Wildli fe Service, Fish Bulletin 74, Vol. 53, 1953.
4I Marine Research, Inc. 1973-1977. (Entrainment Studies). See
, Appendix B.
Marine Research Institute. 1976-1977. (Impingement Study) . See r Appendix B. i3 J Mass. Dept. of Fisheries, Wildlife, and Recreational Vehicles, Div. of Marine Fisheries. 1976-1977. (Screenwash mon 2. coring for impingement) . See Appendix B. Warfel, H.E., and Merriman, D. 1944. Studies on the Marine Resources of Southern New England. I. An Analysis of the Fish Population of the Shore Zone. Bull, of Bingh. Oceanographic 'i 'l Coll. Vol. 9, pp. 2-91. References for 6.14 (Alewife) L Belding, D.L. 1921. A Report upon the Ale,sife Fisheries of ! i Massachusetts. Division of Marine Fisheries and Game, Dept. of Conservation, Boston, Mass . li Bigelow, H.B., and Schroeder, W.C. 1953. Fishes of the Gulf of Maine. U.S. Fish and Wildlife Service, Fish Bulletin 74,
' Vol. 53, 1953.
l de Sylva, D. 1969. Theoretical Consideration of the Effects of l Heated Effluents on Marine Fishes. In: Krenkel, P.A. and F.L. l Parker (eds.) . Biological As pects of Thermal Pollution. Vanderbilt Univ. Press, pp. 22 9-29 3. 6.15-7
I Edsall, T .A . 1970. The Effect of Temperature on the Rate of Development and Survival of Alewife Eggs and La rvae . Trans. Amer. Fish Soc., 99(2):376-380. Hantsman, A.G. 1946. Heat Stroke in Canadian Maritime Stream Fishes. J. Fish. Res. Bd. , Canada 6 (7) , 7 pp. Kissil, G .W . 1974. Spawning of the Anadromous Alewife, Alosa pseudoharenqus (Wilson) and Alosa aestivalis (Mitchill) in Connecticut Waters. Trans. Amer. Fish Soc. 103(2):312-317. Marcy, B.C. 1969. Age Determinations from Scales of Aloca pseudoharengus (Wilson) and ,A lo s ,_ a es tivali s (Mitchill) in Connecticut Waters. Trans. Amer. Fish Soc. 98 (4) : 622-630. Marine Research, Inc. 1973-1977. (Entraiment Studies). See Appenoix B. Marine Research Institute. 1976-1977. (Impingement Study) . See Appendix B. Mass. Dept. of Fisheries, Wildlife and Recreational Vehicles, Div. of Furine Fisheries. 1976-1977. (Screenwash monitoring for - impingement). See Appendix B. - Stanley, J.G., and Colby, P.J. 1971. Effects of Temperature on Electrolyte Balance and Osmoregulation in the Alewife (Alosa g; eseudoharengus) in Fresh and Sea Water. Trans. Amer. Fish. Soc. 100 (4) : 624-638. E-me E I-I I I I 6.15-8 I l EI
=i
III CONCLUSION The supplemental analyses considered in this report have expanded the data base upon which the conclusions of the 316 Demonstration Pilgrim Nuclear Power Station Units 1 and 2, Boston Edison I Company , July 19 7 5, were based . These analyses demonstrate the basic validity of the conclusions of the 316 Demonstration by 2 considering the most recent data collected at the Pilgrim site subsequent to the 316 Demonstration. The- types of analyses presented in the supplemental analyses are I similar to those utilized in the 316 Demonstration. Conservative assumptions are used in the analyses. Thus, the analysea tend to overestimate the effects of the operation of Pilgrim station Unit 1 and the operation of Units 1 and 2. These conservative
,i- assumptions are discussed in Section I, Introduction, of thin report as well as in conjunction with the individual species
- analysis in Section 11 of this report. Examples of the 1 conservative assumptions are the 100 percent mortality assumed for all organisms entrained, and the failure to use the concept l' of biological compensation in many of the analyses.
.I The results of the analysis for each of the 13 representative imp (.,rtant species are similar to those reported in the July 1975 l 316 Demonstration. The differences for individual species I predictions can in large measure be attributed to annual variability in the abundances of the organisms. For sumaary [ purposes, predicted power plant effect for all the species, for
! which exploitation or cumulative effect has been predicted, is below 10 percent.
lg The purpose of this summarization is for comparison with the g conclusions of the extensive review conducted by J.T. McFadden
,, (1977) on the ability of fish populations to compensate for man-ig inducted exploitation. In summarizing his review, McFadden Lg states on page 172, "...it becomes clear that cases in which
>25 percent of the exploitable age classes in a population have r been removed annually are common." With specific reference to
,~
power station exploitation (page 178) , Mc?adden concludes " . . .the addition of an exploitation rate greater than 25 percent [due to
, the power station] to a pre-existing fishery exploitation of '3 25 percent would not endang a the stock of many spe.cies." The LE' levels of exploitation predicted for the Pilgrim Station f all f ar below the levels suggested as acceptable by McFadden.
Therefore, this supplemental analysis indicates that the conclusion of the 316 Demonstration is correct. Based on an a analysis of impact on 13 representative important species, { Pilgrim station Unit 1 and Pilgrim station Units 1. and 2 with the proposed open cycle _ cooling system will not adversely aff ect the ,
" balanced indigenous population of fish, shellfi.sh, and wildlife."
I m -> I
Feference for Section III I McFadden, J.T. 1377. 1.n Argument Supporting the Reality of Compensation in Fish Populations and a Plea to Let Them Exercise - it. 1%ou Proceedings of the Conf erence on Assessing the Ed.f ucts of Power Plant Induced Mortality in Fd 3 Populations. Permagon Press, pp. 153 - 103. t gi I r i I I 4 I I-L I I I I I III-2 a e
I : I. I I I :
,, APPENDII A r TIIERHAL TOLERANCE DATA 316 DD(ONSTRATION PII4 RIM NUCLEAR NVER STATION - UNITS 1 AND 2 Bosr0N EDISDN COMPANY f .t -
g l l i.
- I lI E
- 1. .
I . . , . - .-.. ,..-_. ..,_ __ _ , _ ._ _-,-._ ,- - - . . ~ - . - - . - - - ~ . - - - - - . _ . - - . - - - -
_ _ . _~ .-_ - . .- I I EIPLANAT10N OF TDNS THDMAL TOLERANCE DATA Tolerance Lbrit (LT50) A measure of resistance to temperature. The upper or lover median tolerance limit (LT30) is defined as the temperature at which
$0 percent of the test animals under consideration are able to rarvive e designated period of time (Doudoroff,1942).
Critical Thermal Maximum (CTM) The temperature at which the locomotory activity becomes I disorganized and the animal loses its ability to escape from conditions that will soon cause its death (Mihursky & Kennedy, 1967). j- _Aeelimation The thermal level to which an individual is physiologically adjusted (Mihursky & Kennedy,1967). Avoidanen Tempersture At the upper avoidance temperature, a fish's ability to discriminate slight temperature differencen becomes a meaningful activity, i.e., the fish
. vill avoir' temperatures that create sufficient stress (Oif t & Vestman,1971).
f Prefetred Temnerature
- I The temperature of marimum frequency of occurrence in the experimental gradient is the preferred temperature determined by noting the response of fish to particular portions of an experimental thermal gradient. However, fish are not always found at their preferred temperature in the field. The physiological state of a fiah (season of the, year, diet) or additional behavioral activities (feeding) may override a purely behavioral l responso to temporature (Oift & Vestmane 1971). The range of temperacures occupied by a fish in its natural environment are also reported here.
A-1
I lethal Temrersture I-( One hundred pareent mortality of the test animals. This may be determined in a bioassay where the test animals are held at a constant temperature until death, or exposed to heating or cooling at a standard rate until death. Optimum Orowth Tentwrature Maximum rate of growth occurs at Utis temperature. I 3 gi II. II I I I I. Ij A-2 n,
7 m' a
~m M M m m M' W WWwKm m m m-~m--
Acanthohaustorius allisi - Amphipod I. Mortality Lethal Temp. (F) Life Stage Exposure Time Acclimation Temp. (F) Data Source 97 (1) 77 Sameoto, 1969b,
- p. 2287 III. Reproduction Optimum Temp.
Temp. (F) Range (F) Season Data Source 41.9+ April-August Samecto, 1969a, peak June p. 1337 NOTE: (1) Rise in temperature of 1.8 F per minute beginning at acctirsation temperature until death s 4.0
Alosa pseudoharengus - Alewife
- 1. Mortality Acclination Temp. (F) Data Source Lethal Temp. (F) Life Stage Exposure Time 60.8 Stanley & Colby, 1971, 37.4 (L) adult (1) p. 629 60 .B Stanley & Colby, 1971, 87.8 adult (1) p. 629 III. Reproduction Optimum Temp.
Season Location Data Source Temp. (F) Range (F) Chesapeake Bay Mansueti & Hardy, 1967, Migration 39.6-62.0 p. 57 Kalamazoo River Edsall, 1970, p. 378 60-82 May y Spawnfng Gulf .3f Maine Bigelow & Schroeder,
# 55-60 1953, p. 103 Chesapeake Bay Mansueti & liardy,1967, 39.6-62.0 Mar.-Apr.
- p. 57 Edsall, 1970, p. 379 15 days Incubation / 45 Hatch Edsall, 1970, p. 379 68-70 3.9 days Edsall, 1970, p. 379 84 2.1 days 6 days Bigelow & Schroeder, 60 1953, p. 103 Edsall, 1970, p. 378 63 44.4-84.9 M M M M M M M M M M M M-EM M M M M -. , amme. e. , .,
i
~ ~ ~ '
y y. y q y- y-Alosa pseudoharengus - Alewife p. 2 III. Reproduction Optimum Temp. Temp. (F) Range (F) Time Location Data Source Incubation / 68 3-5 days Chesapeake Bay Mansueti & Ilardy,1967, liatch p. 58 72 2-4 days Massachusetts Bay Belding, 1921, p. 13 IV. Preferred Temperature Avoidance Temp. Acclimation Temp. (F) Range (F) Life Stage Temp. (F) Season Data Source 68 adults 64 Meldrim & Cift, 1971,
- p. 27 y 71 adults 70 Meldrim & Cift, 1971, f, p. 27 79 adults 63 Nov. Heldrim & Cift, 1971,
- p. 34 76 adults 64 Oct. Neldrim & Cift, 1971,
- p. 34 86 adults 7? Aug. Meldrim & Cift, 1971,
- p. 34 NOTE:
(1) Change in temperature of 4.5 F per day beginning at acclimation temperature
t i Ascophyllum nodosum - Rockveed ; I. Mortality i Lethal Temp. (F) Life Stage Exposure Time Acclimation Teap. (F) Data Source 93.2-96.8 nallus Fritsch, 1945, p. 382
?
l i I i l - 1 k I O l I I i I f t i f l i . {
. !i i
i j j
,_ ~ -, , , - .
M ^ $' M' M M 'M M ~ M M' 'M M^ M M ^M Brevoortia tyrannus - Atlantic menhaden
- 1. Mortality Acclimation Tolerance Limit (LT50)_ Life Stage Exposure _ Time Temp. (F) Data Source 84 larvae (2) 50 Itoss et al., 1973,
- p. 360 85.4 larvae (2) 59 iloss et al., 1973,
- p. 360 91.4 juveniles Lewis & Ilettler, 1968, p. 349 93.2 juveniles 161 hr 69.8 Lewis & Hettler, 1968, p. 347 96 juveniles 2 hr 75.2 Lewis & Itettler,
>s 1968, p. 347 4
95 juveniles 22 hr 80.6 Lewis & Itettler, 1968, p. 347 94.6 juveniles 77 hr 84.2 Lewis & IIettler, 1968, p. 347 86 adult 24 hr Engstrom & Kirkwood, 1974, p. 14 38.2(L) larvae 72 hr 44.6 Lwis, 1965,
- p. 411(l) 39.4(L) larvae 72 hr 50 Lewis, 1965,
- p. 411(l) 40.0(L) larvae 72 hr 54.5 Lewis, 1965,
- p. 411(I) 41.4(L) larvae 72 hr 59.0 Lewis, 1965,
- p. 411(l)
Brevoortia tyrannus - Atlantic menhaden, p. 2 I. Mortality Acclimattoa Tolerance Limit (LT50)(F) Life Stage Exposure Time Temp. (F) _, Data Source 41(L) juveniles 98 hr 60.6 Lewis & IIettler, 1968, p. 348 41(L) juveniles 191 hr 64.4 Lewis & liettler, 1968, p. 348 Acc11mation Lethal Temp. (F) Life Stage Exposure Time Temp. (F) Data Source 37.4(L) larvae June & Chamberlin, 1959, p. 43 90 adults Fairbanks, et al., 1971, p. 42 T II. Reproduction co Optimum Temp. Temp. (F) Range (F) Location Season Data Source Spawning 55-80 Long Island May-Oct. Perlmutter, 1939,
- p. 17 56-74 Long Island June-Oct. Wheatland, 1956,
. p. 248 Time - Incubation / 72 48 hr Kuntz & Radcliffe, lla tch 1917, p. 122 i 5 m M M M M - E M M- M- M .. M M M M
.m m m m m m m M M'M M ~ M M M Brevoortia tyrannus - Atlantic menhaden, p. 3 IV. Preferred Temperature Avoidance Temp. Acc11mation Temp. (F) Range (F) Life Stage Season Location Temp. (F) Data Source 34.2-72.0 larvae June-July Narragansett flerman , 1963, Bay p. 107
>50 adults Bigelow & Schroeder, 1953, p. 117 46.6-75.0 adulto July-Nov. New Haven, Warfel & Merriman, Ct. 1944, p. 35, 65 70 adults June Delaware R. 79 Meldrim & Cift, 1971, p. 27 78 adults June Delaware R. 69 Meldrim & Cif t, 1971, p. 34 83 adults June Delaware R. 72 Meldrim & Gift, T 1971, p. 34 m
86 adults July Delaware R. 70 Meldrim & Cfft, 1971, p. 34 85 adults Aug. Delaware R. 77 Meldrim & Gift, 1971, p. 34 90 adults Aug. Delaware R. 81 Meldrim & Cift, 1971, p. 34 Note: (1) Brett (1970, p. 525) figured these temperatures by graphical interpolation of Lewis' work (L) Lower thernal tolerance limit or lethal temperature (2) Transfer of larvae directly from acclimation temperature to increased temperature. IIeld at increased temperature until death.
Chondrus crispus - Irish Moss
- 1. Mortality Lethal Temp. (F) Life Stage Exposure Time Acclimation Temp. (F) Data Source 80 tetraspores 4-10 days Prince, 1971, p. 117 80 carposporma 4 days Prince, 1971, p. 117 95-104 carpospores and 6 min 53 Prince, 1971, p. 143, tetraspores 160 104 carpospores and 1 min 53 Prince, 1971, p. 143 tetraspores 80 mature plants 35 days 53 Prince, 1971, p. 151 from tetraspores 100.4 spores 0.5-6 min 71.6 Marine Research, 1974,
- p. 8 ;
1 II. Crowth O < Optimum Temp. (F) Temp. Range (F) life Stage Data Source 70 53-75 carpospores and Prince, 1971, , retraspores p. 107-8 ' Spore Attachment 40- 80 Frince, 1971, p. 108 i I CS M M M l M M M M M M M
,- m .- m r , , ,
7 ., _. . .. m m - ~m M b M' W M W m' M ' M M M M llomarus americanus - American lobster I. Mortality Tolerance Limit (LTso) (F) Life Stage Exposure Time Acclimation Temp. (F) Data Source 78.2 adult 48 hr 41 McLeese, 1956, p. 259 83.2 adult 48 hr 59 McLeese, 1956, p. 259 86.9 adult 48 hr 77 McLeese, 1956, p. 259 84.5 larvae Engstrom & Kirkwood 1974, p. 14 79.7 adult 48.2 McLeese, 1956, p. 255 i 35.2 (L) adult 48 hr 62.6 McLeese, 1956, p. 263 41 (L) adult 48 hr 81.5 McLeese, 1956, p. 263
> Lethal Temp (F) s 75.2 larvae Templec:an , 1936, p. 494-495 77 Chaisson, 1932, p. 5 34 (L) adult 24 hr 69-70 Wood, 1885, p. 32 CTM (F) 89.6-95.8 84.2-93.2 larvae 59-77 Huntsman & Sparks, 1924
- p. 100 89.6 78.8 1arvae 50-59 Huntsman & Sparks, 1924,
- p. 100 t
llociatus americanus - American lobster, p. 2 II. Growth Optimum Temp. (F) Data Source 71.6-75.2 Hughes et al., 1972, p. 1110 64.4-72.2 Ilughes & Matthiessen, 1962, i p. 416 III. Reproduction Optimum Temp. Ilatching Temp. (F) Range (F) Season Data Source 68 54.5-83.3 June-August Lund&dtewart, 1970, p. 48 68 59+ Beginning in May llughes & Matthiessen 1962, p. 415 8 50.8-57.4 June to August Templeman, 1936, p. 495 ea 46.6 50 weeks Perkins, 1971, p. 98 ; IV. Preferred Temperature (F) Life Stage Acclimation Temp. (F) Data Source 29-75 McLeese & Wilder, 1964, p. 5 Note: (L) Lower thermal tolerance limit or lethal temperature i 33 M M M M MI M M M M M M M M
-- . - m -
- - -~ -- - - - -
M M M~ -
~
W k'h &~M M M M 'M M M M Littorina littorea - Comon periwinkle
- 1. Mortality Acclimation Tolerance Limit (LT50)(F) Life Stage Exposure Time Temp. (F) Data Source 99.6-102.2 adult 6-10 hr 59 Newell et al., 1971,
- p. 529-530 102.2 adult 5.5 hr Fraenkel, 1960, p. 177 103.8 adult 90-120 min Fraenkel, 1960, p. 177 106 adult I hr Fraenkel, 1960, p. 177 114.8 adult 68 Evans, 1948, p. 167 Lethal Temp. (F) 104 adult 11.5-12 hr Evans, 1948, p. 171 T> 105.8-110.6 adult (1) Gowanloch & Hayes.
1926, p. 152 ta 113 adult (1) Fraenkel, 1960, p. 177 114.8 adult 129 hr (1) 68 Mayes, 1929, p. 428 115.9 adult (1) Cowanloch & Hayes, 1926, p. 152 IV. Preferred Temp. (F) Life Stage Locality Data Source 64.4 adult New Brunswick Hayes, 1929, p. 424
<70 adult Southern limit Wells, 1965, p. 40 Note:
(1) Rise in re=perature of 1.8 F per 5 minutes beginning at acclimation temperature until death
Menidie menidia - Atlantic silversid2
- 1. Mortality Tolerance Limit (LT50)(F) Life Stage Erposure Time Acclimation Temp. (F) Data Source 73.4-77 "small fish" 5-13 min 57.2 AEC 1972, p. 5-7 83.1-86.7 "small fish" 5-13 min 69.8 AEC. 1972, p. 5-7 71.6 juvenile 72 hr 44.6 Hoff & Westman, 1966,
- p. 134 77 juvenila 72 hr 57.2 Hoff & Westman, 1966,
- p. 134 86.8 juvenile 72 hr 69.8 Hoff & Westman, 1966,
- p. 134 90.5 juvenile 72 hr 82.4 Hoff & Westman, 1966,
- p. 134 88 adult 3 hr Engstrom & Kirkwood, p
a 1974, p. 14 c 47.6 (L) juvenile 72 hr 82.4 Hoff & Westman, 1966,
- p. 134 39.8 (L) juvenile 72 hr 69.8 Hoff & Westman, 1966,
- p. 134 57.2 Hoff & Westman, 1966, 35.6 (L) juvenile 72 hr
- p. 134 44.6 Hoff & Westman, 1966, 34.7 (L) juvenile 72 hr
- p. 134 CTH (F) Life Stage 72.5 Gift & Westman, 1971, 98.4 94 age 1
- p. 32 77.0 Cift & Westman, 1971, 98.9 93.5 age I
- p. 32 GE M M M M E M M m m m m m
- . ~ ,-. .. ; _.
- .- i i >
.w Menidia menidia - Atlantic silverside, p. 2 Lethal Temp (F) Cnt(F) Life Stage Exposure Time Acclimation Temp. (F1 Data Source 90 87 sdults Fairbanks et al., 1971,
- p. 42 80 adults 64.4 Pearce et al.,1968, cite <1 in AEC, 1972, p. 5-59 89.6 24 hr 59 Fearce, 1969, p. 229 90.5 adults 2 hr 62.2 Pearce et al ,1968, cited in Fairbanks et al. ,1971,
- p. 42 111. Repreduction Optimum Temp.
Spawni.ig Temp.(F) Range (F) Season Location Data Source South.'rn New 8 6&& May-July Bigelow & Schroeder, 1953, (n England Coast p. 303
<59 May-July Long Island Weatland, 1956, p. 263 59-73 May Long Island Perlmutter,1939, p. 23 Incubation / Optimum Temp.
Hatch Temp.(F) Ranee (F) Time 72 F 8-9 days Kuntz & Radcliffe, 1917,
- p. 127 W
Menidia menidia - Atlantic silverside, p. 3 IV. Preferred Temperature Avoidance Temp. Acclimation Temp.(F) Range (F) Life Stage Season Location Temp.(F) Data Source 34 + young fry & Bigelow & Schroeder, adults 1953, p. 303 58.6-73.4 1arvae Herman, 1963, p. 107 52.8-74.8 larvae May-August Perlmutter, 1939, p. 55 39.6-80.2 adult April-Dec. New Haven, CT k'arfel & Merriman, 1944, '
- p. 10, 65 59 young-of-the Nov.-Dec. Delaware R. 43-46 Meldrim & Cift, 1971, year p. 23 y 70 yo.mg-o f-the Nov. Delaware R. 57 Meldrim & Gift, 1971, ;
1 year *
- p. 28 m
74 young-o f-th e May or Oct. Delaware R. 61-63 Meldrim & Cift, 1971, year p. 28 76 young-of-the June Delaware R. 68 Heldriu & Gift, 1971, year p. 28 75 young-of-the- Oct. Delaware R. 70 Meldrin a Gift, 1971, year p. 28 74 young-of-the- Aug. Delaware R. 77 Meldrim & Gift, 1971, year p. 28 68 young-of-the- Dec. Delaware R. 48 Meldrim & Cif t, 1971, year p. 35 55 M M M M M M M M M M M M M M
- ~ m. -
J . ,,3 i4
..., gi,......., .,,
W W
-o'.~ ,
W M M M
~
M M 'M M M M M M MMMM M Menidia menidia - Atlantic silverside, p. 4 Avoidance Temp. Acclimation Terap. (F) Range (F) Life Stage Season location Temp.(F) Data Source 75 young-of-the- Dec. Delaware R. 48 Meldrim & Cift, 1971, year p. 35 84 young-of-the- Oct. Delaware R. 54 Meldria & Cift, 1971, year p. 35 Nov. Delaware R. 57 Meldrim & Cift, 1971, 81 young-of-the-year p. 35 84 young-of-the- Nov. Delaware R. 57-9 Meldrim & Gif t, 1971, year p. 35 young-of-the- Oct. Delaware R. 60 Meldrim & Cift, 1971, 82 year p. 35 8 young-of-the- Oct. Delaware R. 63 Meldria & Cift, 1971, [ 84 year p. 35 I young-of-tbe- Sept. Delaware R. 65 Meldrim & Gift, 1971, 90 year o. 35 85-88 young-of-the- Oct. Delaware p. 67-68 Meldrim & Gift, 1971, year p. 35 68 Meldria & Gift, 1971, 87-92 young-of-the June- Delaware R. year July p. 35 85 young-of-the- Aug.- Delaware R. 74-75 MelJrim & Cift, 1971, year Sept. p. 35 Aug. Delaware R. 77 Meldrim & Cift, 1971, 91-92 young-of-the-year p. 35 i m
Henidia menidia - Atlantic silverside, p. 5 Avoidance Temp. Acclimation Temp. (F) Range (F) Life Stage Seasoq Locatfon Temp.(F) Data Source 97 youna -of-the- July De;ev r R. 79 Heldrim & Gift, 1971, year p. 35 94 young-of-the- July Deitware R. 80 Meldria er Gift. 1971, year p. 35 85 age 1 Aug. Creat r' v 77 Gift & Westman, 1^71, or Barnehat p. 32 Bay, N.J, 86.5 age I Sept. Creat Bay 72.5 Gift & Westman, 1971, or Barnegat p. 32 Bay, N.J. 68-77 young-of-the ' Jan. Delaware R. 41 Heldrim et al.,1974, p. 33 year s
-a 73 young-of-the- Nov. Delaware R. 46 Meldrim et al.,1974, p. 34 year 74 young-of-the- April Delaware R. 54 Meldrim et al.,1974, p. 33 year 75 young-of-the- Oct. Delaware R. 55 Meldrim et al. ,1974, p. 33 year L
77 young-of-the- Oct. Delaware R. 59 Meldrim et al. ,1974, p. 34 year [M M M M M M M M M M M M M M M M M M M
M M M W W W W M 'E'M M M M M M M M M M Menidia menidia - Atlantic silverside, p. 6 Avoidance Temp. Acclimation Temp.(F) Range (F) Life Stage Season location Temp.(F) ? < g.e , e, 81 young-of-the- Oct. Delaware R. 61 twin at al. ,1974, p. 34 year 84-87 young-of-the- May Delaware R. 63 Meldrim et al., 1974, p. 34 year 90 young-of-the- Sept. Delaware R. 73 Meldria et al., 1974, p. 33
, year young-of-the- Aug. Delaware R. 75 Meldrim et al., 1974, p. 34 94 year 93 young-of-the- Aug. Delaware R. 77 Meldrim et al., 1974, p. 34 year July- Delaware R. 79 Meldrim et al. ,1974, p. 33 93-95 young-of-the-year Aug.
y e 81 Meldria et al., 1974, p. 34
$ 86 young-of-the- Aug. Delaware R.
year young-of-the- Aug. Delaware R. 82 Meldrim et al., 1977, p. 34 89 year , Note: (L) lower thermal tolerance limit
11ytilus edulis - Blue mussel
- 1. Plot tality
. Tolerance Limit (LTsn)(F) Life StaEe Exposure Time Acclimation Temp. (F) Data Source 7d.8 s14 days 29.6 Read a Cumming, 1967, p. 151 80.6 s 4 days 34.6 Read & Cuming, 1967, p. ISI 82.4 + 2 days 39 Read & Cuming, 1967, p. 151 Lethal Temp. (F) -
105.4 (1) 59 P2nderson, 1929, p. 407 77 larvae 16-17 days Brenko & Calabrese, i 1969, p. 225 64 adult 14 hours Ritchie, 192 7, p. 14 o 80.6 645 hours Pearce, 1969, p. 230 82.4 41 hours Pearce, 1969, p. 230 86 (2) 45.5 Read & Cuming, 1967, p. 151-2 80 Wells & Cray, 1960 cited in Read & Cuming, 1967, p. 149 can aus aus uma me men aus sus sus amm em aus am aus man as sans seus sus
. . . .- == ~
= . _L-. _ - _ _ _ _ _ . _ _ _ _ _ _ - _ _ _ _ _ _: -'
~ ~
3 Mytilus edulis - Blue mussel, p. 2 II. Crowth Optimun Temp. Temp. (F)- Range (F) Life Stage Data Source 68 59-68 larvae Brenko & Calabrese, 1969,
- p. 225 60.8 50-69.8 larvae Bayne, 1965, p. 7, 22 51.8-57.2 58.1-68.9 larvae Lough, 1974, p. 76 III. Reproduction Optimum Temp.
Temp. (F) Range (F) Season Data Snurce Spawning 60.8-64.4 Bayne, 1965, p. 5 60 April-June Loosanoff, 1943, p. 26
- p Settling 54.5-66.2 54.5-71.6 June-August Allen, 1955, p. 107-8 57-74 June-August Engle & Loosanoff. 1944
- p. 438. Fig. 3; p. 435, Fig. 1
) <75.2 Pearce, 1969, p. 231 IV. Preferred Temperature Optimum Temp. Temp. (F)_ Range (F) Data Source 30-80 Hutchins, 1947, p. 330 41-68 Brenko & Calabrese, 1969,
- p. 225
Mytilus edulis - Blue mussel, p. 3 IV. Preferred Temperature Optimum Temp. Temp. (F) Range (F) Data Source 38.3-66.2 Lough, 1974, p. 75-76 50-77 Widdows, 1973, p. 275 Note: (1) Rise in temperature of 1.8 F per 5 minutes beginning at acc11mation temperature until death (2) Rise in temperature of 1.8 F per 3 to 5 days beginning at acclimation temperature until death
>s kJ 9J i
- l t
m m ,
MM E E E E M M U U E E E M M M E' E~ K Osmerus mordax - Rainbow Smelt
- 1. Mortality Lethal Temp.(F) Life Stage Exposure Time Acclimation Temp. (F) Data Source 70.7-83.3 adult 50-59 Huntsman & Sparks. 1924,
- p. 103 111. Reproduction Optimum Temp.
Temp. (F) Range (F) Season Location Data Source Higration 40-60 March-May Hingham, MA Kendall, 1927, p. 233 Spawning 50-57 by May Massachusetts Bay Bigelow & Schroeder, 1953,
- p. 137 Incubation / 47.3 22 days Massachusetts Bay Crestin, 1973, p. 42 Hatch
' 3' 42.5 19 days Creen Lake. IE Kendall, 1927, p. 341
- sv 57 13 days Massachusetts Kendall, 1927, p. 340 4G-42 42 days Long Island Kendall. 1927, p. 333-334 40-65 3 days Long Island Kendall, 1927, p. 335 37-58 30 days Long Island Kendall, 1927, p. 334
Pseudopleuronectes americanus - Winter flounder
- 1. Mortality Tolerance Limit (LTsnl(F) Life Stage Exposure Time Acclimation Tem. (F) Data Source 66.2 adult 24 hr 39.2 McCracken, 1963, p. 575 71.6 adult 24 hr 50 McCracken, 1963, p. 575 75.2 adult 24 hr 59 McCracken, 1963, p. 575 79.7 adult 24 hr 68 McCracken, 1963, p. 375 71.6 juvenile 72 hr 44.6 Hoff & Westman, 1966,
- p. 135 74.6 juvenile 72 hr 57.2 11of f & Westman, 1966,
- p. 135 juvenile 72 hr 69.8 Iloff & Westman, 1966, 80.6
- p. 135 y
e 84.4 juvenile 72 hr 82.4 Hoff & Westman, 1966, $ p. 135 71.1-74.7 small fish 5-13 min 57.2 AEC, 1972, p. 5-7 77.0-80.6 small fish 5-13 min 69.8 AEC, 1972, p. 5-7 Life Stage Acc11mation Temp.(F) Data Source CTM(F) 68.9 Cift & Westman, 1971, 89.2-89.7 87.3-88.0 young-of -the-year
- p. 43 71.6 Cift & Westman, 1971, 88.9 87 age I
- p. 43 young-of-the-year 74.3 Cift & Westman, 1971, 89.4 87.3
- p. 43 young-of-the-year 76.6 Cift & Westman, 1971, 89.8 88.5
- p. 43 EM M M m m a e as a y a g g g g g g g g c - . . -- . .
M M M M W W M Mh&Mb&h m a mm m 2 Pseudopleuronectes americanus - Winter flounder, p. AccIlmation Life Stage Temp. (F) Data Source Tolerance Limit (LTsn) (F) CD1 Avoidance l Pearce, et al., 88 Adult 1968 (cited in Fairbanks, et al., 1971,
- p. 29)
Acclimation Exposure Time Temp. (F) Data Source Life Stage 69.8 lioff & Westman, juvenile 72 hr 34.6 (L) 1966, p. 135 82.4 Iloff & Westman, juvenile 72 hr 42.8 (L) 1966, p. 135 Acc11mation Exposure Time Temp. (F) Data Source Lethal Temp. (F) Life Stage l 41 Frame, 1973, j 8 75.2 age I
- p. 616 w
Ut j Pearce, 1969, 48 hr 77 p. 228 50-59 Huntsman & Sparks, juvenile (1) 1924, p. 107-8 82.2-87 50-59 Huntsman & Sparks, adult (1) 1924, p. 107-8 81.5-85 53.6-61 Britton, 1924, adult p. 417 83.0-88.6 50-61 Britton, 1924, adult 1.25 br 28.6 (L', p. 417 Laurence, 1975, larvac p. 224 35.6 (L)
Pseudopleuronectes americanus - Winter flounder, p. 3
- 11. Crowth F Op timura Temp. i Temp. (F) Range (F) Life Stage Data Sourrf 53.6-60.8 age I Frrme, 1973,
- p. 615-616 46.4 35.6-46.4 larvae Laurence, 1975,
- p. 224 III. Reproduction Optimum Temp.
Temp. (F) Range (F) Season Location Data Source Spawning <39-40.2 Before Georges Bank. Lux et al., 1970, p. 487 April 32-42 Jan.-May New England Bigelow & Schroeder, 1953,
- p. 280 8
w 35.6-41 34-50 Feb.-Apr. Pearev, 1962, p. 17 m 32-35 Woods liole Lux et al., 1970, p. 486 32-37 Cloucester Lux et al., 1970, p. 486 Incuisation/ Ilatch 37-38 15-18 days Bigelow & Schroeder, 1953,
- p. 280 69 15 days Breder, 1921-1922,
- p. 313-314 IV. Preferred Temperature Avoidance Temp. Acclimation Temp. (F) Rangel Q Life Stage Season Location Temp. (F) Data Source S29-70 adult Bigelow & Schroeder, 1953, p. 279 EM M M M N ""E Teb " 'e '7 tE'"
- 3'
-6 Ier-
-.m e.._ _ _ _ .
7._._, . _ . . . . . _ , . _ _ _ . , M M M M M M M WWWYM M M M M M M. M Pseudopleuronectes americanus' - Winter flounde. , p. 4 IV. Preferred Temperature Avoidance Temp. . Acclimation Temp. (F) Range (F) Life Stage Scason Location Temp. (F) Data Source, 53-60 adult Connecticut Thompson et al., 1971, p. 148 42.0-56.0 larvae March-June long Island Whcatland, 1956 Sound p. 295 54-72 larvae May-June Long Island Pear 1 mutter, 1939,
- p. 52 39.6-80.2 adult April-Dec. New Haven, CT. Warfel & Merriman, 1944, p. 17, 65 53.6-59 adult Atlantic Coast McCracken, 1963,
- p. 579
> 63-72 adult Long Island Olla et al., 1969, [ p. 720 a 76 67 adult Nov. Delaware R. 5/ Mendrim & Gift, 1971,
- p. 29, 36 73.4 adult Long Island Olla et al., 1969,
- p. 720 80 young-ef- 68.9 Gift & Westman, 1971, the-year p. 43 75.5 age 1 71.6 Gift & Westman, 1971,
- p. 43 80 young-of- 74.3 Cift & Westman, 1971, the-year p. 43
Pseudopleuronectes americanus - Winter flounder, p. 5 IV. Preferred Temperature Avoidance Temp. Acc11mation Temp. (F)_ Range (F) Life Stage Season Location _ Temp. (F) Data Source 80 young-of- 76.6 Gift & Westman, 1971, the-year p. 43 Note: (1) Hise in temperature of 1.8 F per 5 minutes beginning at acclimation temperature until death (L) Lower thermal tolerance limit or lethal temperature 1 to CD GB M M M W W M M M M M M M M M M M M M
,__-,l
7-- M M M M e mM M~ M M we e e e mwww Pollachius virens - Pollock. I. Mortality Tolerance Limit (LTsn)(F) Life Stage Exposure Time Acclimation Temp.(F) Data Source Britton, 1924, p. 417 82.2(U) adult 3 min Britton, 1924, p. 417 28.6(L) adult III. Reproduction Optimum Temp. Temp. (F) Range (F) Season Location Data Source Spawning 40-43 35-49 late Autumn- Massachusetts Bay Bigelow & Schroeder, early Winter 1953, p. 215-216 Temp. Range (F) Time 43-49 6-9 days Bigelow & Schroeder, Incubation / 1953, p. 216 Y llatch w w Bigelow & Schroeder, ti 1953, p. 216 IV. Preferred Tenperature Temp. Range (F) Location Data Source 42.8-55.4 Nova Scotia Steele, 1963, p. 1272 34.0+ Scotian Shelf & Steele, 1963, p. 1272 Gulf of St. Lawrence 32-52 Gulf of Maine Bigelow & Lehroeder, 1953, p. 215 Mote: (U) Upper thermal tolerance limit (L) Lower thermal tolerance limit
Tautogolabrus adsperous - Cunner I. Mortality Acclimation Temp.(F) Data A urce Lethal Temp. (F) Life Stage Exposure Time 64.4-71.6 Ilaugaara . Irving.
>82.4-84.2 juvenile 1943, p. 24 l
33.8-37.4 11augaard & Irt ing
>77-78.8 juvenile 1943, p. 24 64.4-71.6 Ilaugaard & ~rving
<41 juvenile 1943, p. 24 33.8-37.4 11augaard & Irving
<33 Juvenil" 1943, p. 24 III. Reproduction Optimum Temp. Data Source Range (F) Season Location Temp.(F)
> Bigelow & Schroeder, s
55+ late spring - u Spawning 1953, p. 475 early summer Wewcantic R., Mass. Serchuk, 1972, p. 69 51.8-85.4 April-August Incubation / Culf of Maine Bigelow & d'chroeder, 55-65 3 days Ilatch 1953, p. 476 Bigelow & Schroeder, 70-72 40 hr 1953, p. 476 Long Island Wheatland, 1956, 50+ May-october Spawning p. 273 Narragansett Bay 11erman, 1963, p. 107 52.7-76.0 May-September ( Long Island Sound Perlmutter, 1939, 46.2-79.9 May-September
- p. 63-64 Long Island Sound Williams, 1967, 50.0-78.8 May-october CD M M M M W m W W W W m=~ m -
a m mP- Q g g
~
--. - - - .- - ,. ;-. n ~-
Tautogolabrus adspersus - Cunner, p. 2 IV. Preferred Temperature Temp. Range (F) Life Stage Location Data Source 68.2-76.0 larvae Narragansett Bay liernan, 1963, p.107 66.4-73 larvae Long Island Sound Wheatland 1956,
- p. 276 50.9-71 larvee Long Island Perlmutter, 1939,
- p. 63-64 32-72 adult Bigelow & Schroeder, +
1953, p. 475-476
>I 44 a
l 3 1 I i a
I THERMAL TOLERANCE DATA LITERATURE CITED I 316 DEMONSTRATION PILGRIM NUCLEAR POWER STATION - UNITS 1 AND 2 Allen, F.E. 1955. Identity of breeding temperatures in southern and northern hemisphere species of Mytilus (Lamellibranchia). Pac. Sci. 9:107-109. Atomic Energy Commission. 1972. Final environmental statement related to construction of Shoreham Nuclear Pow 2r Station, Long Island Lighting I Company, Docket No. 50-322. U.S. Atomic Energy Commission, Directora:.e E of Licensing, Washington, D.C., 505 pp, W Bayne, B.L. 1965. Growth and delay of metamorphosis of the larvae of a Mytilus edulis (L.) Ophelia 2(1):1-47, 3 Belding, D.L. 1921. A report upon the alewife fisheries of Massachusetts. Mass. Dept. Cons., Div. Fish and Game, 135 pp. Bigelow, H.B. and W.C. Schroeder. 1953. Fishes of the Gulf of Maine. U.S. Fish Wildl. Serv. Fish. Bull. 53(4), 577 pp. Breder, C.M., Jr. 1921-1922. Some embryonic and larval stages of the _. winter flounder. Bull. U.S. Bur. Fish, 38:311-315. Brenko, M.H. and A. Calabrese. 1969. The combined effects of salinity and temperature on larvae of the mussel Mytilus edulis. Mar. Biol. 4:224-226. Brett, J.R. 1970. Temperature. Fishes functional responses. In: "
- 0. Kinne, ed. Marine ecology. Vol. 1. Environmental factors, Pt. 1. 3 John Wiley & Sons, Ltd., New York, pp._515-560. E Britton, S.W. 1924. Effects of extreme temperature on fishes. Am. I J. Physiol. 67(2):411-421. ,
Chaisson, A.F. 1932. Factors in shipping of live lobsters from eastern . Nova Scotia. Bull. Biol. Bd. Canada 33:3-29. Crestin, D.S. 1973. Some aspects of the biology of adults and early life stages of the rainbow smelt, Osmerus mordax (Mitchell), from the ! Weweantic River Estuary, Wareham - Marion, Massachusetts, 1968. M.S. . thesis, Univ. of Mass., Amherst, 108 pp. I I I, A-32 gg
=l
I
- Doudoroff, P. 1942. The resistance and acclimatization of marine fishes to temperature changes. I. Experiments with Girella nigricans (Ayres).
Biol. Bull., Woods Hole 83:219-244. Edsall, T.A. 1970. The effect of temperature on the rate of development and survival of alewife eggs and larvae. Trans. Amer. Fish. Soc. 99(2): 376-380. Engle, J.B. and V.L. Loosanoff. 1944. On season of attachment of larvae I. of Mytilus edulis Linn. Ecology 25(4):433-440. I Engstrom, D.G. and J.B. Kirkwood. 1974. Median tolerance limits of selected marine fish and lobster larvae to temperature and chlorinity. I' Supplement to pre-operational report on Pilgrim Nuclear Station. Mass. Div. Mar Fish. In: Marine ecology studies related to the operation I of Pilgrim Station. Semi-annual Report N . 4, January 1974 through June [ 1974, Sec. IIB.3, Boston Edison Company, p. 1-15. Evans, ".G. 1948. The lethal temperatures of some common British littoral 7 g molluscs. J. Anim. Ecol. 17(2):165-173. Fairbanks, R. B., W.S. Collings, and W. T. Sides. 1971. An assessment { ' t. of the effects of electrical power generation on marine resources in the Cape Cod Canal, Mass. Dept. Nat. Res., Div. Mar Fish., 48 pp.
; Fraenkel, G. 1960. Lethal high temperatures for three marine invertebrates:
g Limulus polyphemus, Littorina littorea, and Pagurus longicarpus. Oikos 11(2): 171-182. I~b Frame, D. W. 1973. Conversion efficiency and survival of young winter g flounder (Pseudopleuronectes americanus) under experimental conditions. Trans. Amer. Fish. Soc. 102(3):614-617. 1 [hM Fritsch, F.E. 1945. University Press, Cambridge, 791 pp. The structure and reproduction of the algae, Vol. II.,
~
Gift, J.J. and J.R. Westman. 1971. Responses of some estuarine fishes to increasing thermal gradients. Dept. of Environmental Sciences, Rutgers Univ., 154 pp. Gowanloch, J.N. and F.R. Hayes. 1926. Contributions to the study of marine gastropods. I. The physical factors, behavior, and intertidal [- life of Littorina. Contrib. Can. Biol. Fish. 3(4):133-165. L Haugaard, N. and L. Irving. 1943. The influence of temperature upon the oxygm.2 consumption of the cuener (Tautogolabrus,adspersus Walbaum) in summer and in winter. J. Cell. Comp. Physiol. 21(1):19-26. Hayes, F.R. 1929. Contributions to the study of marine gastropods. III. i Development, growth and behavior of Littorina. Contrib. Can. Biol. s Fish. 4 (26):415-430. I . A-33 1
I Henderson, J.T. 1929. Lethal temperatures of Lamellibranchiata. Contrib. Can. .Biol. Fish 4(25):397-412.
~
Herman, S.S. 1963. Planktonic fish eggs and larvae of Narragansett Bay. Limnol. Oceanogr. 8(1):103-109. Hoff, J.G. and J.R. Westman. 1966. The temperature tolerance < of three species of marine fishes. J. Mar. Res. 24(2):131-140 g . Hoss, D.E., W.F. Hettler, Jr., L.C. Coston. 1973. Ef fecu of thermal , shock on larval estuarine fish - Ecological implica " ns i h respect to entrainment in power plant cooling systems. Ir ~ ' 1.' history of fish. The Proceedings of an International -
'i - .ae ~
Dunstaffnage Marine Research Laboratory of t.. Piological Association at Oban, Scotland, from May l' .. Hughes, J.T. and G.C. Matthiessen. 1962. -
'.ogy of the American lobster, Homarus americanus, i t 4-421.
Hughes, J.T., J.J. Sullivan, and R. Shleser. . ina a ;eographical _ distribution. Ecol. Monogr. 17(3):325-33' E* gi -June, F.C. and J.L. Chamberlin. 1959. The role of the estuary in the life history and biology of the Atlantic menhaden. Gulf. Caribb. Fish. Inst. Proc. llth. Ann. Ses . (1958) 11:41-45. v. Kendall, W.C. 1927. The smelts. Bull. U.S. Bur Fish. 42:217-375. ,- Kuntz, A. and L. Radcliffe. 1917. Notes on the embryology and larval development of twelve teleostean fishes. Bull U.S. Bur. Fish. (1915-1916) , 35:87-134. E g-Laurence, G.C. 1975. Laboratory growth and metabolism of the winter flounder Pseudopleuronectes americanus from hatching through metamorphosis .at three temperatures. Mar. Biol. 32:223-239. .. Lewis, R.M. 1965. The effect of minimum temperaturc on the survival of larval Atlantic menhaden, Brevoortia tyrannus. Trans. Amer. Fish. Soc. 94(4):409-412. - Lewis, R.M. and W.F. Hettler,Jr. 1968. Effect of temperature and salinity 3 on the survival of young Atlantic menhaden, Brevoortia tyrannus. Trans. 5 Amer. Fish. Soc. 97(4):344-349. I A-34 I
Loosanoff, V.L. 1943. Potential mussel production analyzed. Atl. Fisherman 24:12 and 26, Sept. 1943. Lough, R. G. 1974. A re-evaluation of the combined effects of temperature
.. and salinity on survival and growth of Mytilus edulis larvae using response surface techniques. Proc. Natl. Shellfish. Assoc. 64:73-76.
{ W Lund, W.A., Jr. and L.L. Stewart. 1970. Abundance and distribution of j larval lobsters, Homarus americanus, off the coast of southern New I England. Proc. Natl. Shellfish. Assoc. 60:40-49. Lux, F.E., A.E. Peterson, Jr. and R.F. Hutton, 1970. Geographical variation in fin ray number in winter flounder, Pseudopleuronectes t' I americanus (Walbaum), off Massachusetts. Trans. Amer. Fish. Soc. 99(3): 483-488.
)
j Mansueti, A.J. and J.D. Hardy, Jr. 1967. Development of fishes of the Chesapeake Bay Region: An atlas of egg, larval and juvenile stages, Pt.I. Nat. Res. Inst., Univ. Maryland. Port City Press, Baltimore, Md. .j 202 pp. Marine Research, Inc. 1974. Entrainment studies - Pilgrin Nuclear Power ] Station. January - March 1974. In: Marine ecology studies related to the operation of Pilgrim Station. Semi-annual Report No. 4, January 1974 through June 1974, Sec. IIC.1, p. 1-9, Boston Edison Company. I McCracken, F.D. 1963. Seasonal movements of the winter flounder, W Pseudopleuronectes americanus (Walbaum), on the Atlantic coast. J. Fish. Res. Bd. Canada 20T2):551-586. McLeese, D.W. 1956. Effects of temperature, salinity and oxygen on the survival of the American lobster. J. Fish. Res. Bd. Canada 13(2):247-272. McLeese, D.W. and D. G. Wilder. 1964 Lobster storage and shipment. Fish. Res. Bd. Canada Bull. 147, 69 pp. p I Meldrim, J.W., amd J.J. Gift. 1971. Temperature preference, avoidance and shock experiments with estuarine fishes. Bull. No. 7, 75 pp. Ichthyological Assoc., k Meldrim, J.W., J.J. Gift, and B.R. Petrosky. 1974. The effect of tempera-ture and chemical pollutants on the behaviour of several estuarine organisms. Ichthyological Assoc., Bull. No, 11, 129 pp. Mihursky, J.A. and V.S. Kennedy. 1967. Water temperature criteria to protect aquatic life. Amer. Fish. Soc. Spec. Publ. No. 4:20-32. Newell, R.C., V.I. Pye, and M. Ahsanullah. 1971. The effect of thermal acclimation on the heat tolerance of the intertidal prosobranchs Littorina littorea (L.) and Monodonta lineata (DaCosta) J. Exp. Biol. 54(2):525-533. I A-35
l Olla, B.L., R. Wicklund, and S. Wilk. 1969. Behavior of winter flounder , in a natural habitat. Trans. Amer. Fish. Soc. 98(4):717-720. Pearce, J.B. 1969. Thermal additions and the benthos, Cape Cod Canal. Chesapeake Sci. 10(3+4):227-233. Pearce, J.B., M. Silverman, and R. LeGoff. 1968. Laboratory investiga-tions of the effects of thermal additions on marine organisms character- g istic of Cape Cod Canal. Sandy Hook Marine Laboratory, Highlands , N.J. , g 21 pp. (cited in Fairbanks, et al., 1971). . Pearcy, W.G. 1962. Ecology of an estuarine population of winter flounder, Pseudopleuronectes americanus (Walbaum). II. Distribution and dynamics of larvae. Bull. Bingham Oceanogr. Collect. Yale Univ. 18(1):16-37. Perkins, H.C. 1971. Developmental rates at various temperatures of embryos of northern lobster (Homarus americanus Milne-Edwards). Fish. $ Bull. 70(1):95-99. Perlmutter, A. 1939. A biological survey of the salt waters of Long Island, 1938. Section I. An ecological survey of young fish eggs identified from tow-net collections. Suppl. 28th Ann. Rept., N.Y. Conserv. Dept., Pt. II:ll-71. p Prince, J.S. 1971. An ecological study of the marine red alga, Chondrus ll crispus, in the waters off Plymouth, Mass. Ph.D. thesis, Cornell Univ., E 191 pp. Read, K.R.H. and K.B. Cumming. 1967. Thermal tolerance of the bivalve - molluscs Modiolus modiolus L., Mytilus edulis L. and Brachidontes demissus Dillwyn. Comp. Biochem. Physiol. 22(1):149-155. [ ~ Ritchie, J. 1927. Reports on the prevention of the growth of mussels in submarine shaf ts and tunnels at Westbank Eltetric Station, Portobello. . icans. Roy. Scot. Arts (December 29, 1921):1-20. E{. E-Sameoto, D.D. 1969a. Some aspects of the ecology and life cycle of i three species of subtidal sand-burrowing amphipods (Crustacea:Haustariidae). ' J. Fish. Res. Bd. Canada 26:1321-1345. Sameoto, D.D. 1969b. Physiological tolerances and behavior responses of five species of Haustoriidae (Amphipoda: Crustacea) to five environmental factors. J. Fish. Res Bd. Canada 26(9):2283-2298. Serchuk, F.M. 1972. The ecology of the cunner, Tautogolabrus adspersus, 3 (Walbaum) (Pisces:Labridae), in the Weweantic River estuary, Wareham, 5 Massachusects. M.S. thesis, Univ. Mass., Amherst, 93 pp. I I , A-36 I , E'i m
1 I I t [ Stanley, J.G. and P.J. Colby. 1971. Effects of temperature on electrolyte
, balance and osmoregulation in the alewife (Alosa pseudoharengus) in i fresh and sea water. Trans. Amer. Fish. Soc. 100 (4):624-638. l Steele, D.H. 1963. Pollock (Pollachius virens (L.)) in the Bay of r Fundy. J. Fish. Res. Bd. Canada 20(5):1267-1314.
Templeman, W. 1936. The influence of temperature, salinity, light, and -,. food conditions on the survival and growth of the larvae of the lobster, Homarus americanus. J. Biol. Bd. Canada 2(5):485-497. Thompson, K.S., W.H. Weed, III, and A.G. Taruski. 1971. Saltwater j fishes of Connecticut. Conn. State Geol. Nat. Hist. Surv. Bull. 105, 165 pp. Warfel, H.E Merriman. 1944. Studies on the marine resources of 1 southern N e' - An analysis of the fish population of the shore zone
. i Oceanogr. Collect. Yale Univ. 9(2):1-91.
I Wells, H.W. 1r . m ords of the gastropod, Littorina littorea, Il with a discust - 7 trolling its southern distribution. ,E Chesapeake Sci. 7,
, g Wella,, H.W. and I.E. .. y . The seasonal occurrence of Mytilus 5 edulis on the Carolina coast a. a result of transport around Cape Hatteras. . Biol. Bull., Woods Hole. 119:550-559. (Cited in Read and Cumming, lL 1967.)
45 kleatland, S.B. 1956. Oceanography of Long Island Sound, 1952-1954. VII. Pelagic fish eggs and larvae. Bull. Bingham Oceanogr. Collect. Yale Univ. 15:234-314. t- Widdows, J. 1973. Effect of temperature and food on the heart beat, } ventilation rate, and oxygen uptake of Mytilus edulis, Mar. Biol. 20:269-276. Williams, G.C. 1967. Identification and seasonal size changes of the labrid fishes, Tautogolabrus adspersus and Tautoga onitis, of Long Island Sound. Copeia 1967(2):452-453. I ~j ' Wood, W.H. 1885. Transplanting lobsters to the Chesapeake - Experiments upon the temperature which they can endure. Bull U.S. Fish, Comm.
,. 5:31-32.
I I I A-37
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3 24 tg - .r' APPENDIX B
- t i!
LIST OF MARINE ECOLOGICAL AND HYDRAULIC STUDIES lr.- ASSOCIATED WITF. PILGRIM STATION il b i5 ks' l( . I I
.i .
I La lI LI I I
1
, l APPENDIX B l LIST OF MARINE ECOLOGICAL AND HYDRAULIC STUDIES 4
ASSOCIATED WITH PILGRIM STATION Proiect(*) Contractor-Consultant-Agency Study Periodtt), Marine Ecology
- 1. Marine Ecology Surveys Mass. Department of Fisheries, 1968-1977 (finfish, lobster, Wildlife and Recreational sport fishery, dis- Vehicles, Division of Marine solved gases, water Fisheries (MDMF) temp., and Irish moss)
- 2. Benthic Studies a. Raytheon Marine Lab. 1969-1970
- b. Clapp Laboratories, Battelle 1971-1974 I Memorial Inst.
- c. Dr. A. Michael (Marine Biological lab. , (MBL) and 1974-1977
~ I Yale U.), Dr. R.D. Wilce (U. Mass.)
- 3. Ichthyoplankton Survey of Cape Cod Bay Marine Research, Inc. (M .R .I .) 1974-1976
- 4. Entrainment Studies M.R.I. 1973-1977
- 5. Screenwash Monitoring MDMF 1973-1975 for Impingement
-6.'Lnpingement Study Marine Research Institute 1976-1977 (Dr. B.L. Marshall) 7 . Winter Flounder M.R.I. 1976-1977 Larvae Studies
- 8. Lobster Larvae Studies M.R.I. 1974-1976
- 9. Water Quality Dr. D. Carritt (U. Mass .) 1973 Measurements
- 10. Temperature and Clapp Laboratories, 1972-1974 I Chlorine Tolerance MeaLurements Batte12: Memorial Institute
- 11. Life History Study Cornell Univ. 1969-1971 of Chondrus crispus (J . Prince)
- 12. Menhaden Gas-Bubble New England Aquarium 1974-1976 Tolerance Studies
- 13. Irish Moss Woods Hole Oceanographic 1974-1976 Quality Surveys Institution (Dr. J.H. Ryther et al)
APPENDIX B (CONT 'D) J Proiect Contractor-consultant-Agency Study Period
- 14. Pilgrim Unit 1 Mass. DMF/BECO/ Marine Research 1973-1977 Intake Monitoring Institute
- 15. Study of Alternative Yankee Atomic Service 1975-1977 Solutions to Menhaden Company /EGSG Attraction Probleau
- 16. Fish Barrier Study 1).R.I. (Dr. G. Mott) 1973-1977 B. Thtrmal Plume and I Oc::anographic C- 'ies
- 1. Model Development and a. MIT (Dr. D.R.F. Harleman et al) 1972-1977 Predictions of Thermal b. Dr. D.W. Pritchard 1970-1974 Plume Behavior. (Johns Hopkins Univ.) 3
- c. EGSG, Environmental 1974-1975 5 ,
Equipment Division p
- 2. Winter Flounder 1975-1977 I MIT (Dr. B. F. Pearce)
Larvae Model Development
- 3. Field Measurements of Unit 1 Thermal Plume 3a. Boat Surveys a. MIT 1972-1973
- b. VAST, Inc. Dec. 1972 .
- c. EGSG Oct. 1974 '
3b. Aerial Infrared a. Coastal Research Corp. Dec. 1974 Surveya b. Aero-Marine Surveys, Inc. Aug. 1973 ,-
- c. Environmental Protection Agency Sept.1974 3 ,~
Oct. 1975 E 3c. Dye Release Studies a. Westinghouse "one Research 1971 g
- b. Vast, Inc. Dec. 1972 3
- c. EGSG Oct. 1974
- 4. Oceanographic a. MDMF 1968-1977 Measurements b. Endeco-Mr. R. O'Hagan 1973-1975 (ambient temperature c. EGSG 1974-1975 and currents)
-5. Analyses Related a. Dames S Moore 1967 to Physical Ocean- b. Dr. D.W. Pritchard (Johns 1970-1974 3 ography and Thermal Hopkins Univ.) E --
Plume - (in addition c. Stone S Webster Environmental 1974
- to above) Engineering Division
- d. Yankee Atomic Service Co. 1975 (
C. Alternate Cooling Bechtel Corp. 1971-1975 B-2 I E '
APPEMDIX B (CONT 'D) Pro-iect Contractor-Consultant-Agency Study Peri od System Studies r@ o Impact Analysis for Stone & Webster Environmental 1975-1977 L Selected Marine Specier Engineering Division
- . (*) Refer to Pilgrim Unit 1 and 2 4R and Pilgrim Station Semi-Annual Marine Ecology Series for scope description and individual study results. -
(2) Inclusive periods including extensions into the future wherever contractual arrangements have been made. l I I I I I I I I P L --
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