ML030140515
| ML030140515 | |
| Person / Time | |
|---|---|
| Site: | Ginna  |
| Issue date: | 12/23/2002 |
| From: | Mecredy R Rochester Gas & Electric Corp |
| To: | Robert Schaaf Document Control Desk, Office of Nuclear Reactor Regulation |
| References | |
| Download: ML030140515 (119) | |
Text
TABLE OF CONTENTS CHAPTER 4:
TEMPERATURE TOLERANCE INFORMATION AND AREAS OF EXCLUSION Section Page 4.1 DISCHARGE CONSIDERATIONS..............................
- 4.1-1 4.2 THERMAL EFFECTS UPON RIS................................
4.2-1
4.2.1 Macroflora
Cladophora...........
............. 4.2-6 Maximum for Survival of Parent.................
4.2-6 Maximum for Summer Survival...................
4.2-7 Optimum Growth..................................
4.2-7 Maximum for Developmento...
4.2-7 Normal Reproduction Dates and Temperatures.... 4.2-8 Summary........................................
4.2-8
4.2.2 Macroinvertebrates
Gammarus................. 4.2-10 Maximum for Survival of Parent................
4.2-10 Maximum for Summer Survival..................
4.2-10 Adults..............................
4.2-10 Eggs and Immature Forms..............
4.2-11 Optimum Growth..................................
4.2-11 Adults...............................
4.2-11 Immatures...........................
4.2-12 Maximum for Development.........................
4.2-12 Reproduction Dates and Temperatures........... 4.2-13 Summary..........................................
4.2-13 4.2.3 Fish...........................................
4.2-15 4.2.3.1 Alewife..............................
4.2-18 Maximum for Survival of Parent....... 4.2-18 Maximum for Summer Survival.........
4.2-19 Optimum Growth......................
4.2-20 Acceptable Growth....................
4.2-21 Maximum for Development and Reproduction.......................
4.2-21 Potential for Cold Shock..,,.,,.....
4.2-22 Summary..............................
4.2-24 4.2.3.2 American Smelt......................
4.2-24 Maximum for Parental Survival.......
4.2-25 Maximum for Summer Survival.........
4.2-25 Optimum Growth........................
4.2-25 Reproduction........................
4.2-26 Maximum for Development.............
4.2-26 Potential for Cold Shock............
4.2-26 Summary.............................
4.2-28 4.2.3.3 Spottail Shiner....................
, 4.2-28 Maximum for Parental Survival.......
4.2-28 Maximum for Summer Survival.........
4.2-29 Optimum Growth........................
4.2-29 Acceptable Growth...................
4.2-30 Maximum for Development and Reproduction.........................
4.2-30 Potential for Cold Shock............
4.2-30 Summary..............................
4.2-32 4-i
Section Page 4.2.3.4 White Perch...........
4.2-32 Maximum for Parental Survival.......
A.2-32 Maximum for Summer Survival.........
4.2-3 2 Optimum Growth......................
4.2-33 Acceptable Growth...................
4.2-33 Maximum for Development Reproduction.....................
o 4 Potential for Cold Shock.........4.2-34.23 Summary.......
... 4.2-35 4.2.3.5 Smallmouth Bass.....................
4.2-36 Maximum for Survival of Parents.....4.2-36 Maximum for Summer Survival.........
4.2-36 Optimum Growth............
o.........
4.2-37 Acceptable Growth o.......
4.2-37 Maximum for Development............. 4.2-37 Reproduction................
. 4.2-38 Potential for Cold Shock............
4.2-38 Summary..............
o..... o.......
o4.2-38 4.2.3.6 Coho Salmon..........................
4.2-39 Maximum for Survival During Reproductive Season.................
4.2-39 Maximum for Summer Survival.........
4.2-40 Optimum Growth....................
4.2-40 Acceptable Growth...................
4.2-40 Reproduction and Maximum for Development....................
4.2-41 Potential for Cold Shock............
4.2-Al Summary....
4.2-42 4.2.3.7 Brown Trout........
. 4.2-42 Maximum for Parental Survival......
4.2-42 Maximum for Summer Survival.......
A.-)3 Acceptable Growth...................
4.2-44 Reproduction and Development........
4.2-44 Potential for Cldo Shock............
4.2-44 Summary......
o......................
4.2-46 References.......................................
4.2-47 4-ii
LIST OF TABLES TABLE NUMBER 4.2-1 4.2-2(1) 4.2-2 (2) 4.2-2(3) 4.2-2 (4) 4.2-2(5) 4.2-2 (6) 4.2-2(7) 4.2-2 (8) 4.2-3(1) 4.2-3(2) 4.2-3(3) 4.2-3(4) 4.2-3(5)
TITLE Average Monthly and Seasonal Intake Temperatures -
Ginna Nuclear Power Station RIS Temperature Data Sheet Cladophora and Gammarus Temperature Data Sheet Alewife (Alosa pseudoharengus)
Temperature Data Sheet American Smelt (Osmerus mordax)
Temperature Data Sheet Spottail Shiner (Notropis hudsonius)
Temperature Data Sheet White Perch (Morone americana)
Temperature Data Sheet Smallmouth Bass (Micropterus dolomieui)
Temperature Data Sheet Coho Salmon (Oncorhynchus kisutch)
Temperature Data Sheet Brown Trout (Salmo trutta)
Evaluation of Thermal Data Cladophora glomerata Evaluation of Thermal Data Gammarus fasciatus Evaluation of Thermal Data Alewife (Alosa pseudoharengus)
Evaluation of Thermal Data American Smelt (Osmerus mordax)
Evaluation of Thermal Data Spottail Shiner (Notropis hudsonius) 4-iii
LIST OF TABLES (Cont'd)
TABLE NUMBER 4.2-3(6) 4.2-3(7) 4.2-3(8) 4.2-3(9)
TITLE Evaluation of Thermal Data White Perch (Morone americana)
Evaluation of Thermal Data Smallmouth Bass (Micropterus dolomieui)
Evaluation of Thermal Data Coho Salmon (Oncorhynchus kisutch)
Evaluation of Thermal Data Brown Trout (Salmo trutta)
Lower Thermal Tolerance of RIS - Fish as Related to Discharge and Ambient Water Temperatures 0C (OF) 4.2-4 4-iv
LIST OF FIGURES (Cont'd)
TITLE Nomograph to Determine the Maximum Weekly Average Temperature of Plumes for Various Ambient Temperatures OC (OF)
(EPA, 1974) 4-v FIGURE NUMBER 4.2-1
CHAPTER 4.0 TEMPERATURE TOLERANCE INFORMATION AND AREAS OF EXCLUSION 4.1 Discharge Considerations Chapter 4.0 contains a quantitative theoretical assessment of thermal effects on representative important species (RIS) pre sent within a defined discharge zone.
Evaluation is focused on the discharge zone, rather than the mixing zone (Section 1.5).
Such a limitation permits a much more realistic and reliable interpretation of potential impact because of the high frequency of plume occurrence in the discharge zone; whereas the expansive mixing zone, encompassing the discharge zone and all possible extreme plumes, contains large areas with only brief intermittent plume contact.
Because of infrequent and unpredictive plume penetration much beyond the discharge zone, the applicant will not address mixing zone impacts except in a qualitative sense where needed.
The discharge zone selected is defined in Section 1.5 as the segment of a circle encompassing the 30F isotherm of an expected spring plume deflected east and west, containing 175.7 surface acres and having a radius of 3374 feet from the point of discharge.
Size of the discharge zone at a depth of 6 feet is 64.9 acres and 2357 feet (linear extent); that portion of the discharge zone in contact with lake bottom encompasses 10.7 acres and extends 1029 feet lake ward from the point of discharge (note Section 1.4.2.2 and Figures 1.4-67 through 69).
4.1-1
Areas within each 1 F (0.55°C) increment of the discharge zone, at each of three depths (surface, 6 feet, and bottom) are presented in Table 1.5-1.
These areas are incorporated with information on thermal sensitivities of various biological activities, for each RIS in Section 4.2, to develop and evaluate a theoretical impact of the Ginna discharge on biota within the discharge zone.
Evaluation of thermally impacted areas on the lake bottom must be viewed in perspective with a scour zone contained within the bottom portion of the discharge zone.
The scour zone has been defined in subsection 1.4.3.1.2 as being that bottom region along the plume centerline near shore, which is bounded by a 1 fps velocity isopleth; it encompasses an average area of 2.8 acres, or a maximum of 5.2 acres (note Section 1.4.3.1.2 and Figure 1.4-82).
Loose substrates such as silt, sand, and fine gravel in conjunction with their less productive associated fauna, are usually swept free from the scour zone.
- However, benthic organisms residing in crevices and on the down-current side of boulder sized rocks possibly remain unaffected by current velocity within this region.
Organisms typically flourishing within mats of Cladophora may be somewhat reduced in proportion to the limitation on Cladophora biomass and filament length.
To assess the overall impact of scouring it should be recognized that many benthic forms are capable of inhabiting more than one type of substrate.
Thus it is doubtful to expect that physical scouring will eliminate specific species. Instead, scouring will tend to reduce the population sizes relative to ambient conditions.
4.1-2
4.2 Thermal Effects Upon RIS This section contains a detailed evaluation of theoretical thermal plume effects within a previously defined discharge zone (see Section 1.5).
Since the discharge zone is defined to be the 3°F isotherm as required by the New York State thermal criteria (6 NYCRR 704) and since, as this chapter will clearly demonstrate, the impact within the discharge zone is negligible, the applicant does not anticipate any effects within the adjacent water body segment.
In compliance with the EPA guidelines for this demonstration, the applicant will evaluate thermal effects of the discharge during each of four seasons.
The thermal regime of each season is pre sented in Table 4.2-1, including individual monthly average temperatures.
Winter, consisting of January, February, and
- March, is characterized by an average ambient lake temperature of 1.3 0 C (34.4 0 F).
The spring season (average 8.1 0 C or 46.5 0 F) consists of April, May, and June; while the summer season consists of July, August, and September, and has an average ambient lake temperature of 18.8 0 C (65.8 0 F).
Fall consists of October, November, and December, and has an average ambient temperature of 8.2 0 C (46.80F).
If, during the course of analysis, the applicant finds that a particular life activity extends for more than one season, but less than two seasons, the impact will also be evaluated for mean temperatures in those months apart from the principal season in which the activity occurs.
In addition to seasonal and/or monthly evaluations, the applicant has chosen to address specific times 4.2-1
during the year when average ambient temperatures are exceeded for a brief period.
All of these additional time segments occur during the summer season.
For ten percent of the year, or 37 days during the summer, the maximum temperature of ambient lake water will be 21.1 C (70.0°F) cr greater.
During five percent of the year (18 days),
ambient lake water will be 22.2 0 C (720F),
or greater.
For one percent of the year (four days) ambient lake temperature will be 23.9 0 C (75°F); this is the single maximum ambient temper ature expected.
Evaluation of thermal effects on Cladophora (Section 4.2.1),
macro invertebrates (Section 4.2.2),
and fish eggs deposited on the bottom (Section 4.2.3), will focus on a small portion of the benthic habitat where the plume makes bottom contact.
Analysis is restrict ed to this zone because it is the only place where these particular RIS organisms and eggs may be potentially impacted.
Within this area of bottom contact, ranging in size from less than 5.1 acres to a maximum 10.7 acres and extending 1029 feet lakeward, is a
physically impacted region termed the scour zone.
The scour zone will occupy an average area of 2.8 acres (maximum 5.2 acres) along the main axis of the plume, and be bound by a 1.0 fps velocity isopleth (see Section 1.4.3.1.2 and 4.1).
The impact evaluation on fish is more complex since these organisms may occupy various levels within the water column, and the size of the discharge zone diminishes with depth.
To facilitate evaluation, the discharge zone and associated isotherms are described for the lake surface and 6-foot depth (note Section 1.4).
The expected 4.2-2
spring plume, deflected both east and west, is used to derive the discharge zone (refer to Section 1.5); area at the surface is 175.7 acres, and 64.9 acres at a depth of six feet.
Since fish are rarely confined to the upper one foot of the water column, where the surface discharge zone applies, evaluation at the six-foot isotherms is a better indicator for potential effects.
Fish listed as being taken in "top" nets at Ginna are actually caught in the upper five to six feet of the water column, thus supporting the need to consider both areas within the discharge zone.
Thermal effects are determined by comparing ambient and discharge temperatures with threshold sensitivity temperatures for various life activities of each RIS (sensitivity based on data in Tables 4.2-2(1) through (8)).
The actual comparisons and resultant areas within the discharge zone, from which various activities may be excluded or limited on the basis of excessive temperatures, are provided in Tables 4.2-3(1) through (9).
Concerning the response of fish to these specific areas, the 316(a)
Guidance Manual (EPA, 1974, p. 101) states, "...there are both vertical and horizontal thermal gradients that mobile organisms can follow to avoid unfavorable high (or low) temperatures".
Therefore, exclusion could simply take the form of avoidance.
All impact areas indicated are in the epilimnetic zone, thus sensitive species found in the hypolimnion will not be affected.
4.2-3
Impact areas and temperatures presented in the discussions below represent a conservative discharge zone, especially since this zone is normally twice the expected plume size (Table 1.5-3),
and include the range of expected plume areas (bounded by 3*F isotherms) for all seasons.
The state regulations imply that temperature increases less than 3°F are not expected to inter fere with a balanced indigenous population of aquatic life (6NYCRR 704.1).
Thus, there are no thermal effects of any sig nificance anticipated for the adjacent water body segment.
Thermal effects discussed in Sections 4.2.1 to 4.2.3 are grouped according to the general categories listed in the 316(a) Guidance Manual (EPA, 1974).
Where possible, upper lethal temperatures were interpolated using existing data in Tables 4.2-2(1) to (8) and prevalent ambient lake temperature as the acclimation temper ature for the appropriate month or season.
Sensitivity temperatures for growth, development, and reproduction, in addition to the appropriate time periods during which these activities occur, were derived for all RIS from the scientific literature.
Specific life activities evaluated for each RIS are (1) maximum temperature for survival of the parent, (2) maximum temperature for summer survival, (3) optimum growth temperature, (4) maximum temperature for accept able growth (where appropriate),
(5) maximum temperature for development, and (6) normal temperatures for reproduction.
A brief description of the thermal evaluation data presented for each RIS in Tables 4.2-3(1) through (9) may simplify subsequent inter-4.2-4
pretation and discussion.
The first column lists specific biological activities under consideration, while the second provides the time of occurrence for each activity (appropriate season, month, or part thereof).
A third column contains ambient lake water tem perature for respective time periods listed in the second column.
The fourth column lists the sensitivity temperature which, when exceeded, could potentially impact the aforementioned biological activity.
The column titled "isotherm exceeding sensitivity temperature" contains the lowest isotherm of the discharge zone that exceeds the sensitivity temperature during the appropriate time period (thus it equals Column 4 minus Column 3).
The remain ing columns provide (1) areas, in acres, from which the biological activity is excluded; (2) the area of exclusion represented as a percentage of the total surface area of the discharge zone; and (3) the number of days during which the activity is limited or excluded.
4.2-5
4.2.1 Macroflora
Cladophora The discussion presented below is a theoretical evaluation of thermal impact upon Cladophora, and is based upon temperature sensitivity data cited in Table 4.2-3(1) for various life activities.
As previously indicated in Section 4.2 any impact evaluation on Cladophora must center about that portion of the discharge zone which contacts the lake bottom out to a water depth of about three meters, and encompasses an area of 10.7 acres.
Maximum for Survival of Parent The maximum temperature for survival of a reproducing Cladophora filament is about 22.2 C (72°F),
as derived from the work of Storr and Sweeney (1971).
This temperature would not be exceeded within the discharge zone during the early spring (April and May) and late fall (November and December) portions of the Cladophora reproductive period.
In the months of June and October this temperature may be exceeded within an area considerably less than 5.1 acres in size (note Table 4.2-3(1)).
Concerning the summer period, parent survival may be limited within 6.5 to 10.7 acres of the bottom contact region for about 74 days.
For the remainder of summer, ambient lake water temperatures will equal or exceed the sensitivity temperature of 22.2 0 C (72°F),
thereby naturally repressing this life activity.
4.2-6
Maximum for Summer Survival The applicant has observed a short stubble of viable Cladophora in the discharge waters at Ginna during the summer.
This would in dicate that the Cladophora filament, though greatly shortened, can withstand temperatures of 32.2 C (90°F) and possibly greater.
Using 32.2 0 C (90 F) as a conservative estimate for sensitivity, the applicant predicts an elimination of Cladophora filament within an area less than 5.1 acres for about 18 days during the summer season.
Optimum Growth Based on the results of Storr and Sweeney (1971),
the temperature for optimum growth of Cladophora is 18.0 0 C (64.4 0 F).
Within the spring season, growth would be suboptimal within less than 5.1 acres, or less than 2.9 percent of the discharge zone in May and June.
During the entire summer, average ambient lake water temper ature in Lake Ontario exceeds 18.0°C (64.4 0 F),
thereby naturally resulting in suboptimal growth throughout the southern shoreline area.
Conditions in the fall season are expected to be the same as for spring, growth is repressed within a bottom-contact area of less than 5.1 acres.
No adverse impact is predicted for December or the winter months.
Maximum for Development This activity is not applicable to Cladophora because its reproduc-4.2-7
tive cells vegetate directly into a filament.
Normal Reproduction Dates and Temperatures Cladophora may reproduce variously during spring, early summer, and fall.
A very conservative upper limit of sensitivity for re production may be taken as 18.0°C (64.4 F).
This temperature may be exceeded within less than 5.1 acres of the bottom discharge zone in May, June, October, and November.
During the summer, average ambient water temperatures will naturally exceed this sensitivity.
Cladophora is not necessarily eliminated by excessive temperature.
The alga often produces resistant thick-walled cells termed akinetes, which are unaffected by subjection to excessive temperature.
Upon the return of favorable conditions, these cells may germinate and recolonize the area.
Summary To summarize the predicted thermal impact on Cladophora one must realistically consider the acreages cited above in relation to the scour zone.
As discussed in Section 4.1, a maximum area of 5.2 acres may be physically scoured by the Ginna surface discharge.
Life activities and biomass of Cladophora will be greatly limited within this zone by turbulence associated with discharge flow; any additional impact due to plume temperatures would be negligible.
Therefore, reviewing each of the acreages listed in Table 4.2-3(1) and subtracting 5.2 acres for scour, the applicant would predict the following as a more refined theoretical thermal impact:
4.2-8
(a) maximum sensitivity for survival of parent Cladophora will be exceeded at most within a small area of 1.3 acres (0.7 percent of the discharge zone) during 74 days of the summer period, and within about 5.5 acres for 19 days of the summer.
No adverse thermal impact is predicted for spring, fall, and winter.
(b) summer survival, growth, and reproduction of Cladophora will not be impacted outside of the scour zone during any season.
Considering that these potentially thermal impacted areas are extremely small, relative to the total region available for colo nization of Cladophora at the site, it is reasonable to conclude that the Ginna plume has a negligible adverse impact on this species.
4.2-9
4.2.2 Macroinvertebrates
Gammarus An evaluation of thermal impact on various life activities of Gammarus is based on the data presented in Table 4.2-3(2) and discussed below.
As with the evaluation for Cladophora, any impact on Gammarus will be limited to the region of bottom contact between the plume and lake bed.
Maximum for Survival of Parent Based on the work of Sprague (1963),
a conservative maximum tem perature for survival of parent gammarids is 31.0°C (87.80F) in summer.
This temperature is exceeded within an area less than 5.1 acres (less than 2.9 percent of the discharge zone) for 37 days during the warmest part of the summer season (ambient temperatures equal to or in excess of 21.1 C (70°F).
During the remainder of summer, spring and early fall, sensitivity temperatures are suffi ciently high and ambient temperatures low enough so that no part of the plume will thermally impact Gammarus.
Maximum for Summer Survival (a)
Adults Again based on Sprague's (1963) data, adult gammarids can withstand temperatures up to 31.0°C (87.80F) during the warmest part of the summer.
This sensitivity temperature may be exceeded within less than 5.1 acres of the discharge zone for 37 days, or less, 4.2-10
during the warmest part of the summer season (ambient water temperatures equal or in excess of 21.1 C (70 F)).
For the remainder of summer, the sensitivity temperature will not be exceeded in the plume.
(b)
Eggs and Immature Forms Deriving a most conservative upper limit of 26.0°C (78.8 0 F) for summer survival of these forms from Clemens (1950),
one might expect a reduction in abundance at least within less than 5.1 acres throughout summer, and within a maximum 9.3 acres for about 4 days at the peak of summer temperatures.
Optimum Growth (a)
Adults Utilizing 20.0 C (68°F) as a conservative upper limit for optimal growth of adult gammarids, the applicant might expect a theoretical suboptimal growth (smaller sized adults) within less than 5.1 acres of the discharge zone in June, 10.7 acres for about 55 days of the summer season, and less than 5.1 acres in October.
For part of the summer (about 37 days) ambient 4.2-11
water temperatures will exceed the optimum for adult growth and small sized adults will typically result throughout the lake, a condition well documented for Lake Erie (Clemens, 1950).
(b)
Immatures Immature gammarids have a sensitivity temperature of about 25.0°C (77°F) for optimum growth.
Based on this the applicant might expect a suboptimal growth of these forms within an area ranging from less than 5.1 acres to a maximum 10.7 acres for various times during the summer season (note Table 4.2-3(2)).
Maximum for Development An upper limit for the development of eggs and young gammarids was not cited in the literature.
Since Clemens (1950) found eggs and young gammarids in his samples from Lake Erie at times when the ambient temperature was 26.0°C (78.8 F),
it is reasonable to assume that the limit for this activity exceeds 26.0°C (78.80F).
Again for purposes of prediction the applicant selected 26.0°C (78.8°F) as an extremely conservative estimate of sensitivity.
Based on this value, development could be suppressed in an area ranging from less than 5.1 acres for most of the summer, to a maximum of 9.3 acres for 4 days during the warmest ambient temper-4.2-12
ature (23.9 0 C (75 0 F)).
- 5)
Reproduction Dates and Temperature An upper thermal limit for reproduction was not found in the literature.
Gammarus typically reproduce from late March through late October over a complete range of seasonal lake temperatures (Clemens, 1950).
Since Clemens (1950) reported the presence of breeding females at a lake temperature of 26.0 C (78.8°F),
it is presumed that the upper limit must exceed 26.00C (78.8°F).
For predictive purposes the applicant selected 26.0 C (78.8°F) as an extremely conservative estimate of sensitivity.
On this basis, the applicant could expect limited reproduction to occur within less than 5.1 acres for most of summer to a maximum of 9.3 acres for 4 days in mid-summer.
Summary To summarize the thermal impact on Gammarus, one must again consider the scour zone (maximum area 5.2 acres).
The velocity of discharge waters, in addition to a reduction of preferred habitat substrate (Cladophora biomass),
could theoretically limit life activities of Gammarus within the scour zone.
To evaluate areas within the dis charge zone where Gammarus are solely impacted by temperature, one can subtract a scour zone of 5.2 acres from each acreage listed in Table 4.2-3(2).
The following may be deemed a more refined theoretical thermal impact assessment:
4.2-13
(a)
There should not be any area of bottom contact outside of the scour zone where parent gammarids are thermally stressed.
(b)
Eggs and immature forms could be thermally stressed, resulting in reduced survival and suboptimal growth, within about 2.7 acres for 18 days in summer, and a maximum of 5.5 acres for 4 days during the height of ambient summer temperatures.
No adverse impact is predicted for spring and fall.
(c)
Adults may experience slight suboptimal growth within 5.5 acres for 55 days of summer.
(d)
Activities such as development of eggs, and reproduction, may be thermally limited within an area of 4.1 acres for approximately 4 days during summer.
No adverse impact is predicted outside of the scour zone for the remainder of summer, spring, or fall.
Considering the absence of potential thermal impact on survival of adult gammarids, the extremely small areas and brief periods of impact on eggs, immatures, and reproduction, and lastly the predicted suboptimal growth within a small area during summer, it appears unlikely that the Ginna discharge could have a signifi cant, much less a measureable, adverse thermal impact on Gammarus.
4.2-14
4.2.3 Fish As stated in the introduction to Section 4.2, evaluation of theoretical thermal impact on fish distribution is discussed in terms of both the surface and six foot isotherms.
Since few fish occupy the top one foot of the plume where the surface isotherms apply, the six foot isotherms present a more reasonable area for assessing thermal effects.
Since plume bottom contact extends about 1000 feet lakeward to the ten foot depth contour, there will not be adverse thermal effects on fish found below this depth.
Development and reproduction temperatures, where applicable (as in the case of demersal eggs), are evaluated in terms of the areas where the plume contacts the bottom.
Thermal impact in the scour zone, contained within the region of plume bottom contact, is expected to be negligible since many organisms and selected activities such as spawning will be excluded by the scour effect alone.
The scour zone coincides with bottom areas subject to the greatest temperature elevations (delta T's of 7 F and greater).
In evaluating effects which may involve mortality, such as maximum temperature for survival of parents, and maximum temperature for summer survival, the upper lethal temperature (LD50) corresponding to acclimation temperatures (ambient water temperature) is usually reduceC by 20 C (3.6 F) to provide a safe survival temperature for use in Tables 4.2-3(3) through (9).
This assures survival and pro tects the fish from stress effects.
When an upper lethal temperature 4.2-15
is not reported in the scientific literature for a specific acclimation temperature, but other upper lethal temperatures are provided, the unknown is derived by interpolation within the limits of existing values.
Temperatures for optimum growth, reproduction, and development are taken directly as reported in the scientific literature, or from field observations.
Acceptable growth temperature for each RIS is obtained, as set forth by Coutant in the 316(a) Guidance Manual (EPA, 1974) and in NAS (1973),
by adding one-third of the difference between the optimum growth temperature and the ultimate incipient lethal temperature to the existing optimum growth tem perature.
Fish living at this temperature or below are capable of acceptable growth rates.
For each RIS-fish a discussion is provided concerning probable effects of reactor shutdowns on protection and propagation of a balanced indigenous aquatic community at Ginna.
There are two dis tinct types of shutdowns, "scheduled" and "rapid" (unscheduled).
The applicant anticipates a scheduled reactor shutdown once per year, normally in the spring, for refueling and maintenance pur poses.
During the process of shutdown there is a gradual decline in discharge temperature of about 10.6 0 c (190F) over a 20 minute time period.
Rapid shutdowns are unscheduled and may occur anytime within the year for various reasons.
The Ginna facility has had an average of about ten rapid shutdowns per year, with an average down-time 4.2-16
of 16 hours1.851852e-4 days <br />0.00444 hours <br />2.645503e-5 weeks <br />6.088e-6 months <br />.
A temperature drop associated with rapid outage may vary from 10.6 0 C (19 0 F) to 13 0 C (23.4 F),
depending upon season and the degree of recirculation.
Assuming a condition of 10.6 0 C (19 0 F),
the rate of discharge temperature change would approximate 9.8 0 C (17.6 0 F) within the first minute, and 1.0 0 C (1.80F) in the second minute.
From an environmental standpoint, rapid and scheduled shutdowns do not differ sufficiently to require separate evaluations.
A month by month analysis for each RIS fish encompasses both shutdowns.
The potential environmental problem associated with shutdowns is a subjection of organisms, principally fish residing within the heated discharge, to "cold-shock" following removal of the heat component.
Fish can withstand rapid decreases in water temperature, provided ambient lake temperatures are within lower lethal tolerance limits established for a series of acclimation or discharge temper atures.
A reasonable first approximation for impact evaluation can be derived by determining -lower lethal temperatures for individual average monthly discharge temperatures, and comparing these data with ambient lake temperatures.
If lower lethal values based on maximum discharge temperature exceed ambient conditions, a potential for cold-shock could exist within some defined area of the plume.
Con versely, if ambient values exceed lower lethal temperatures, then there is no potential for cold-shock.
To refine cold-shock evaluations and render them more applicable to the Ginna discharge, three additional factors will be considered:
(1) proximity of specific RIS fish populations to the shore region and discharge area for each month and/or season (note Chapter 3);
4.2-17
(2) swimming capability, specifically cruising speed, and thermal preference of each species (note Chapter 3) as they relate to potential distance of penetration into the plume (maximum discharge velocity is about 4.0 fps, at 246 ft USGS lake elevation; note Fig. 1.4-27);
(3) expected plume residence time and extent of acclimation to elevated discharge temperatures, given cruising speed capabilities at available temperatures; acclimation implies stabilizing physiologically to a particular thermal condition, and requires time on the order of days.
The reliability of lower tolerance levels is directly dependent upon acclimation to a particular thermal regime.
4.2.3.1 Alewife Table 4.2-3(3) presents the evaluation of thermal effects upon the alewife.
Maximum for Survival of Parent Maximum temperature for survival of mature alewives is not exceeded anywhere in the plume (surface or six foot depths) during the spring spawning season (including June).
Should spawning extend on into early July (as noted in Carlander 1970),
there is a possibility that mature alewives may be excluded from about 60 acres (34 percent 4.2-18
of the surface discharge zone),
or more realistically from about 19 acres at the six foot depths, for about 15 days.
This would not, however, exclude mature alewives from entering the region under the plume and spawning near the bottom (to be discussed below).
Considering that mature alewives spawn near shore in shallow waters, and considering the wedge shape of the discharge zone which results in the narrowest part of the exclusion zone being closest to shore (the region of great potential impact on spawning),
the applicant is reasonably confident that the Ginna discharge would not adversely impact mature alewives.
Maximum for Summer Survival Since adult alewives have a summer preference temperature of 160C (60.8 0 F),
they are not expected to inhabit near shore waters in summer, thus avoiding potential impact.
The subsequent discussion will center on juveniles which do inhabit nearshore waters.
Analysis of the maximum temperature for summer survival shows that the sensitivity temperature increases with increased acclimation temperatures (note Table 4.2-3(3)).
The maximum isotherm area that exceeds the temperature which assures survival for this period is 20.9 acres (11.9 percent of the discharge zone at the surface) and occurs for only four days during the summer.
The maximum area at the six foot depth is 6.1 acres (3.5 percent of the discharge zone) and this also occurs for only a brief four days.
4.2-19
Considering the maximum duration for exclusion, juvenile alewives may avoid 5.6 acres and 1.5 acres at the surface and six foot depths, respectively for 92 days (the entire summer season).
These are obviously small areas, respresenting 1 to 3 percent of the total discharge zone.
Optimum Growth In examining growth temperature for the alewife, the optimum growth 0
temperature is reviewed first.
Using the value-of 22.7 C obtained from the literature (Table 4.2-2(2)), the maximum area of theoretical impact occurs ten percent of the year (37 days) during the summer within 175.7 acres (100 percent of the discharge zone) at the sur face, and 64.9 acres (36.9 percent of the discharge zone) at the six foot depths.
This assumes a hypothetical worst case condition with alewives remaining in the area of impact continuously for the entire duration of 37 days.
At least two factors enter in to minimize this degree of potential impact; (1) adult alewives will be offshore in summer and avoid the plume waters; (2) the remaining juveniles are pelagic and schooling, thus it is difficult to con ceive having them reside continuously for the duration of impact within the discharge zone.
Aside from the summer season, alewives could potentially experience suboptimal growth in small confined areas of about 2.3 acres (surface),
or 0.7 acres (six foot depth), during the months of June and October.
4.2-20
Acceptable Growth It is apparent from Table 4.2-3(3) that all areas for potential impact on acceptable growth are reduced from optimal growth impact; in addition there are no potential impacts in June and October for either the surface or six foot isotherms.
The largest area of potential impact (suboptimal growth) is about 102 acres (57.8 percent of the surface discharge zone) and 35.2 acres at the six foot depth; this occurs for a brief period of four days.
The potential impact of greatest duration (92 days) encompasses 9.6 acres at the surface (5.5 percent of the discharge zone) and 2.7 acres (1.5 percent) at the six foot depths.
These areas of potential impact are considerably reduced from those for optimum growth temperature, and for the same reasons stated above, represent worst case conditions which are undoubtedly mini mized through alewife behavior patterns.
Maximum for Development and Reproduction Normal reproduction dates and temperatures, as shown on Table 4.2-3(3) occur in the spring with a peak from mid-June to early July.
The normal temperature range for reproduction of the alewife is not exceeded or reached during spring within the plume.
There is a
small area nearshore at the surface of the discharge zone (5.6 acres),
from which reproduction might be excluded in July.
Since alewives spawn near the bottom in shallow water, these potential 5.6 acres 4.2-21
coincide with the maximum scour zone (5.2 acres) where spawning is physically restricted by water flow.
Therefore the applicant does not expect reproduction of alewives to be impacted thermally at the Ginna discharge.
Concerning development, a thermal evaluation finds no area of exclusion within the discharge zone.
Potential For Cold Shock The evaluation for potential cold-shock of alewives centers on the spring, summer, and fall months when ambient nearshore lake tem peratures exceed 3 C (37.4°F).
As previously discussed in Section 3.3.3.2.1, and verified in winter studies by the applicant at Ginna, and in Lake Michigan by Otto et al. (1976),
the alewife population moves offshore by late fall to overwinter in deep warmer
(>3°C) waters; thus avoiding any potential winter impact.
Colby (1973) supports the need for alewives to escape from cold nearshore waters -by experimentally demonstrating their susceptibility to severe stress at temperatures less than 30C (37.4 0 F).
Lower lethal temperatures of alewives, determined for monthly discharge temperatures on the basis of data reported in Otto et al.
(1976),
are provided for each of nine months in Table 4.2-4.
There is an apparent potential for cold-shock following shutdown in only two months, April and December, assuming an unlikely acclimation to a maximum discharge temperature of 15.60C (60 0 F).
To achieve physiological acclimation to 15.60C (60 0 F),
alewives must be capable of maintaining themselves by cruising for many 4.2-22
hours, or more likely days, in a region characterized by a discharge velocity of about 3.5 to 4.4 fps.
Given swimming speed data for alewives in Table 3.3.-5, and extrapolating to 15.6 0 C (60 0F),
it becomes readily apparent that Age II alewives (10.4 cm in length) can only cruise at about 1.2 fps (3.5 body lengths per second);
thus clearly preventing their acclimation to maximum plume temper ature in April and December.
Even larger alewives, up to 15.2 cm (6 inches) could only cruise at about 1.8 fps at 15.6 0 C (60 0 F).
They may penetrate the area of greatest velocity by darting, however they could not maintain themselves sufficiently long to achieve acclimation.
Assuming for conservative predictive purposes that alewives can maintain themselves at a discharge velocity of only 1.8 fps, it is reasonable to query the temperature corresponding to this velocity.
Judging from the discussion on plume velocity in Section 1.4.3.1, and the data in Table 1.4-9, alewives might be capable of penetrating the plume to within about 518 m (1700 feet) from the discharge canal.
Plume temperature is expected to be about 5oC (9 0 F) above ambient at this distance (note Table 1.5-1),
thus alewives could become acclimated to a maximum 9.4 0 C (48.9 0 F) in April, and 9.3 0 C (48.7 0 F) in December.
A lower lethal temperature range for these acclimation temperatures is about 4.1 to 4.150 C (39.4-39.5°F),
and falls slightly below ambient lake conditions of 4.3 to 4.1 0 C (39.7-400 F).
Alewives normally tend to be cold stressed because of ambient conditions in spring, and easily succumb to any additional stress.
4.2-23
A plant shutdown in April has the potential for cold-shocking or stressing some of the alewives presumed to be present and acclimated to a At of 50C (9 0 F) within the plume; the potential is warranted since their lower lethal temperature nearly coincides with ambient.
Relative to the billions of individuals migrating shoreward in spring, and the millions which normally die-off, any loss of specimens accompanying a plant shutdown in April would be negligible and certainly not interfere with the protection and propagation of this species.
Any potential for impact in December, the only other month of concern, would be minimal since most of the population has moved offshore away from the sphere of plume influence.
Summary To summarize potential thermal effects of the Ginna discharge upon the alewife population, the applicant has shown there to be a small area of possible exclusion for mature alewives in July, very small areas or larger areas for brief time periods excluding juveniles in summer, suboptimal growth in various portions of the discharge zone mostly in summer (assuming alewives remain there for weeks or months),
and finally negligible thermal impact on their development and reproduction activities.
On this basis the applicant concludes no appreciable adverse thermal impact on the alewife population.
4.2.3.2 American Smelt Table 4.2-3(4) presents the evaluation of thermal data for the American smelt.
4.2-24
Maximum for Parental Survival To evaluate maximum for parental survival, the applicant selected the maximum temperature at which smelt spawn, 18.3 0 C (64.90F).
Spawning of smelt in Lake Ontario occurs primarily in early spring (April to May).
No impact is expected for early spring since sensitivity temperature is not exceeded within the discharge zone.
Maximum for Summer Survival As discussed in Section 3.3.4.2.1, adult smelt have a very low temperature preferendum and usually move offshore into deeper water either at or below the level of the thermocline.
Therefore adults will not be subject to thermal impact by the Ginna discharge.
Juvenile smelt, however, have a higher preference temperature than adults in summer and may be available for potential impact.
Evalu ation of the data indicates that juveniles could be excluded from about 133 surface acres of the discharge zone, and 47.6 acres at the six foot depth for 55 days.
During the remainder of time in summer, ambient surface temperatures exceed sensitivity temperature.
Optimum Growth In discussing thermal effects on growth for the smelt, it must again be pointed out thdt adult smelt are not found in the warm epilimnetic waters during the summer months.
In fact, ambient surface water temperatures of Lake Ontario exceed optimum temperatures for both adult and juvenile smelt growth in summer.
4.2-25
Reproduction As shown in Table 4.2-2(3),
normal reproduction occurs in waters of temperature up to 14.5 0 C (58.10F) in Lake Ontario from March to usually not later than May, but dates as late as July have been reported in the literature.
The July lake water temperatures are too high for normal spawning, so any spawning which would occur would have to occur in colder streams.
The potential spawning area that might be thermally affected is less than 5.1 acres in size and located within the scour zone.
Since this area will be physically impacted, the potential for adverse thermal effects on reproduction is negligible.
Maximum for Development The maximum temperature for development of smelt eggs is found to be 15 0 C (59.0°F).
During the spring season ambient waters are cooler than this sensitivity temperature.
Eggs are found in less than 0.6 meters (2 feet) of water where they remain attached by means of a pedicel.
In spring, the only bottom area (4.6 acres) within the discharge zone available for impact on egg development is scoured.
There is, therefore, no area within the plume where egg development will be adversely affected by the thermal component of the discharge.
Potential for Cold Shock In the absence of specific experimental data on lower thermal tolerances for smelt, the applicant considers it reasonable to utilize the EPA (1974) nomograph (note Figure 4.2-1) for assessing 4.2-26
potential cold-shock impact.
Smelt are basically cold-water fish which avoid warm nearshore epilimnetic waters in summer.
They do, however, inhabit nearshore areas during spring, fall, and possibly winter.
Examination of the data in Table 4.2-4 indicates a potential for stress on smelt, acclimated to a maximum discharge temperature of 15.6 0 C (60 0 F),
following a plant shutdown in April and December.
Applying the same conservative logic utilized in Section 4.2.3.1 for alewives, it is realistic to presume that smelt (15.2 cm or 6 in.
in length) can swim about 1.8 fps (3.5 body lengths per second),
and thus penetrate only to the 50C (9 0 F) At isotherm during these two months.
Assuming acclimation to a maximum temperature of 9.4 C (48.9°F) in April and December, smelt can safely return to an ambient temperature of 2.2 0 C (36 0 F).
Since ambient conditions in April and December-exceed 2.2 0 C (360F),
the applicant is reasonably confident there will not be a cold-shock impact.
During winter months, it is again presumed that smelt are re stricted from acclimating to temperatures in excess of 9.40C (48.9 0 F); however a lower lethal value of 2.2 0 C (36 0 F) exceeds ambient temperatures and renders the fish susceptible to cold shock in the event of a shutdown at this time.
The extent of potential impact is not presumed to be adverse.
A gill net study conducted by the applicant in February 1975, (RG&E, 1976a) resulted in the capture of only one smelt among all the nets set, which in cluded the plume, E-0 shore, and also W-1 shore areas.
This sug gests that despite a preference for warmer water in winter (10 0 C, see Section 3.3.4.2.1) there does not appear to be a large concen-4.2-27
tration or attraction of smelt to the immediate discharge area, thus minimizing the potential for winter cold-shock.
Summary Due to American smelt's preference for cold water, and its normal distribution in deep, offshore waters in the summer, the potential for thermal impact on this species is expected to be minimal.
Reproduction and development activities would not be thermally impacted outside from the maximum scour zone.
4.2.3.3 Spottail Shiner Table 4.2-3(5) presents the evaluation of thermal data for the spottail shiner.
Maximum for Parental Survival Mature spottail shiners typically spawn in June and July.
Each of these two months is evaluated separately since they represent spring and summer seasons.
Evaluation of ambient and sensitivity temper atures for June indicates no potential impact in the discharge zone.
In July, spottails may be excluded from a small portion of the discharge zone (4.3 acres) close to the discharge canal (within the 9.4 0 C or 17 0 F At isotherm).
At the six foot depth, which is close to the bottom near shore, mature spottails would be thermally excluded from about 1.2 acres; this area is contained within the 4.2-28
scour zone.
Given the small magnitude of these exclusion areas, relative to the available non-impacted areas nearshore at Ginna, the applicant considers the potential for thermal impact to be negligible.
Maximum for Summer Survival Depending upon their vertical location within the discharge zone, and ambient temperatures in summer, spottails may be excluded from a maximum area of 14.5 to 45.8 acres for a brief period of four days in summer, to a minimum of 1.2 to 4.3 for acres for the entire summer (see Table 4.2.3(5)).
Judging from the preference temperature data presented in Table 3.3.3.2-1, and discussed in Section 3.3.5.2, it appears that spottails normally avoid the warmest nearshore waters in summer.
This would tend to minimize the potential for impact in summer.
Optimum Growth In evaluating optimum growth, attention is focused on the summer period since Carlander (1970) states that growth of spottail shiners ceases below 18 0 C (64.4 0 F).
Results of thermal assessment suggest a potential for suboptimal growth of spottails inhabiting about 11 to 176 acres of the discharge zone in summer.
It is doubtful that the potential for impact exists since spottails avoid the plume area in summer (note Section 3.3.5.3).
4.2-29
Acceptable Growth Evaluation of potential impact on acceptable growth results in a
reduction of areas for suboptimal growth to about 3.5 to 133 acres.
Avoidance of the plume by spottails in summer renders this an unlikely life activity for impact.
Maximum for Development and Reproduction A review of the available literature failed to uncover specific incubation and hatch temperatures for spottail shiners.
- However, since hatching occurs shortly after spawning, the temperatures for both processes are assumed to be the same, 20 0 C (68 0 F).
It is reported that spottail shiners spawn near shore in 0.9 to 1.25 meters (3-4 feet) of water.
Evaluation of the thermal data reveals a potential bottom zone of thermal impact (less than 5.1 acres in size) which is coincident with the scour zone.
Spawning is expected to be greatly reduced in the area of scour, and the potential effect on reproduction and development would be negligible since the eggs would be swept away.
Potential for Cold Shock Spottail shiners tend to be somewhat smaller (average length of 11 to 12 cm) than the two previously discussed forage species, and are therefore expected to exhibit a slower cruising speed (1.3 fps, assuming a length of 11.5 cm, and potential for 3.5 body lengths per second).
A limited penetration into the plume (verified by their absence from the discharge canal in TV monitoring studies 4.2-30
(RG&E, 1976b)),
coupled with the spottail shiner's final preference for temperatures below those in the area of maximum discharge velocity, suggests a low potential for cold-shock effects.
Lower lethal tolerances provided for spottail shiners in Table 4.2-4, are interpolated from cold-shock results reported in Reutter and Herdendorf (1974),
and assume (1) a most conser vative winter final preference and acclimation to 12.0°C (53.6 0 F),
(2) a spring and fall final preference (with the exception of June and October) for 14.30C (57.7 0 F),
and (3) a summer preference (including June and October) for 19.5 0 C (67.1 0 F),
see discussion in Section 3.3.5.2.1.
With the possible exception of February, an unexpected plant shutdown at Ginna should not produce measure able cold-shock effects upon spottail shiners.
In the case of February, when ambient temperatures are near 0.90C (33.7 0 F),
there is some uncertainty about realizing 100% survival in the event of a shutdown.
Judging from the applicant's gill net study in Feb ruary 1975 (RG&E, 1976a), relatively few spottails inhabit the nearshore area off Ginna at this time; this lends support to a prediction for minimal potential impact.
An important noteworthy comparison between experimentally derived lower lethal temperatures, and those based on the EPA (1974) nomograph, for spottail shiner (a moderate cold-water species),
will clearly demonstrate a conservative quality in the nomograph below plume temperatures of 13.30C (56 0 F).
This assures the 4.2-31
applicant that cold-shock evaluations based on the nomograph (for species having little or no test data) will be reasonably conser vative for the most critical period, namely winter.
Summary In summary, the applicant anticipates no consequential thermal effects on either reproduction, development, or parent survival within the Ginna discharge zone.
The potential for direct impact on spottails and suboptimal growth within various sized areas in
- summer, is minimized by their natural avoidance of the area at this time.
4.2.3.4 White Perch Table 4.2-3(6) presents the thermal evaluation data for the white perch.
Maximum for Parental Survival Reproduction occurs in the spring and the maximum temperature for parental survival is interpolated from the data available.
A sensitivity temperature of 28 C (82.4°F) is not expected to occur anywhere within the discharge zone in spring, thus there should be no effect on parental survival.
Maximum for Summer Survival Evaluation of temperatures for summer survival shows that the maximum potential area for exclusion is about 21 acres in size at the lake surface, and 6.1 acres at the six foot depth; exclusion 4.2-32
would be extremely brief (4 days).
The size of area impacted for the longest duration (37 days) ranges from 5.6 surface acres to 1.5 acres at six foot depths.
In general these small areas and short duration of exclusion, confined to the warmest part of summer, constitute a minimal potential for impact.
Optimum Growth Evaluation of optimum growth temperatures shows no potential for impact in the discharge zone during late spring (June).
During summer months, white perch could experience suboptimal growth in an area ranging from about 35 to 176 acres at the surface of the discharge zone, and 11 to 65 acres at the six foot depths.
The latter range may be more applicable since white perch are not expected to reside in the surface waters all summer.
Acceptable Growth Examination of acceptable growth temperatures reveals a reduction in the areal extent of potential impacts.
Again there is no impact expected for late spring (June).
During the summer months, a
theoretical suboptimal growth may occur in fish continuously re siding within 7 to 78 acres at the surface region, and 2 to 26 acres at the six foot depths.
The potential for impact may be reduced by the greater availability of food near the plume; growth is regulated not only by temperature but by food supply.
4.2-33
Maximum for Development and Reproduction Examination of the thermal data for development and reproduction activities shows a very small area (less than 5.1 acres) of potential thermal impact which is contained within the scour zone.
Since spawning is not expected to occur, and eggs are not expected to be retained within the scour zone, the potential for thermal impact is considered negligible.
Potential for Cold Shock White perch appear most abundant in the nearshore areas at Ginna during the summer (July and August),
and generally migrate to deeper offshore waters in the fall, remaining there through the winter (note Section 3.3.6).
Since the applicant did encounter some white perch at both plume and control loc ations during the February 1975 gill net survey (range of 4.5-6 fish/net/day),
it was decided to include winter months in the cold-shock evaluation.
Using a most conservative cruising type swimming speed of 3.6 body lengths per second, based on temperatures in excess of 21 0 C (69.8 0 F) (note Table 3.3-5), and assuming an average white perch (15.2 cm (6 in.) in length) can maintain this unlikely speed at reduced temperatures in winter, it becomes readily apparent this species could only achieve acclimation to plume temperatures corresponding to the 1.8 fps isopleth.
According to the plume velocity data in Table 1.4-9, white perch could cruise at a distance about 1700 feet from the point of discharge, a 4.2-34
location characterized by a surface At of about 50C (9 0 F) (See Table 1.5-1).
At worse, this species could acclimate to a maximum temperature of 9.40C (48.9 F) during winter, early spring (April),
and late fall (December).
During all remaining months, acclimation temperature is expected to exceed ambient by about 5OC.
Since specific cold-shock data were not available for white perch, the applicant chose to utilize the EPA (1974) nomograph for impact evaluation, at least in the warmer months.
White perch, and their close relative, white bass, are warm-water fish.
Reutter and Herdendorf (1974) demonstrated that white bass withstand a rapid temperature decline from 13.50C (56.3 0 F) to 0.90C (33.6 0 F) with no apparent stress.
From this it is presumed white perch exhibit a similar capability for an even lower acclimation tem perature during the colder months; this is in keeping with the nomograph evaluation for 9.4°C (48.9 0 F),
which is at least 50 C (9 0 F) above ambient in winter.
A comparison of lower lethal and ambient temperatures in Table 4.2-4, indicates a slight potential for cold-shock effects only in mid-winter (February).
White perch should not experience cold-shock effects following plant shutdown in any other month.
Summary In summary, the applicant finds no potential for thermal impact on reproduction, development, and parent survival within the Ginna discharge zone.
There is a potential for some exclusion of white perch from small areas during the warmest part of summer, and a potential for suboptimal growth in areas of various dimensions 4.2-35
during the summer months.
Enhancement of food reserves in and about the discharge may compensate for thermally induced suboptimal growth, and serve to minimize the extent of potential impact.
4.2.3.5 Smallmouth Bass Table 4.2-3(7) presents the thermal evaluation data for smallmouth bass.
Maximum for Survival of Parents Smallmouth bass reproduce primarily in the spring, but have been known to spawn as late as early July.
Given a sensitivity temper ature of 20.7 C (69.3 F) for survival of parent in spring, the applicant finds no potential for thermal impact within the Ginna discharge zone.
Should spawning extend into early July there is a potential for exclusion of mature fish from about 4.3 acres (2.4 percent) of the surface discharge zone.
The impact is ex pected to be negligible since most spawning activity will have occurred previous to this time.
Maximum for Summer Survival Evaluating the potential temperature effects on summer survival of smallmouth bass, the applicant finds extremely small areas of possible exclusion, ranging from 1.5 to 5.6 acres at the six foot depths and surface region, respectively.
Areas in this size range comprise less than 3.5 percent of the discharge zone.
The potential for impact is limited because smallmouth bass have a distinct preference and tolerance for warm-water habitats (note Section 3.3.7.2.1).
4.2-36
Optimum Growth Examination of the thermal data on optimum growth indicates a potential for limited or suboptimal growth of bass within about 1.2 acres (92 days) to 14.5 acres (4 days) at the six foot depth region.
Areas at the surface are somewhat larger (about 4 to 46 acres),
however less applicable because fish would be expected to spend much less time in that region.
Enhanced production and availability of food resource for bass near the plume may compensate for thermally induced suboptimal growth.
Acceptable Growth Acceptable growth would be even less impacted in terms of time and acreage at the surface and six foot depth.
Areas of potential impact range from about 1 to 5 acres, to 4 to 16 acres at the six foot depths and surface region respectively.
Impact would be limited to 37 days or less during the warmest part of summer.
Maximum for Development The maximum temperature for development is estimated from the literature using the optimum growth temperature for larvae.
This temperature is not exceeded within the discharge zone during spring.
In the summer, the only area for potential impact is con tained within the scour zone, where spawning is expected to be negligible.
Thus the potential for impact on development is negli gible.
4.2-37
Reproduction Reproduction normally occurs in the spring, but may continue as late as July.
Evaluating the potential for impact in the bottom waters, since smallmouth bass are nest builders, one can conclude that there would be no effects in May, no effects in June (area of impact is within the scour zone),
and a limited potential impact within about 4 acres outside from the scour zone in July.
Since most spawning occurs prior to July the overall impact may be re garded as negligible.
Potential for Cold Shock Evaluation of lower thermal tolerance data for smallmouth bass in Table 4.2-4, indicates no potential cold-shock for those individuals acclimated to maximum discharge temperatures during spring, summer, or fall.
Since smallmouth bass migrate offshore and overwinter on the lake bottom, there is no potential for winter cold-shock.
Support is derived by the absence of smallmouth from the discharge area during a winter gill-net study (RG&E, 1976a),
and during TV monitoring in the winter (RG&E, 1976b).
Summary To summarize the findings of a theoretical thermal impact assessment on various life activities of smallmouth bass, one could safely conclude that the Ginna discharge has a negligible impact on development,reproduction, and parent survival, and would exclude 4.2-38
individuals from inhabiting very small areas (less than 3.5 percent of the discharge zone) during the summer.
Growth could be sub optimal within reasonably small subsurface areas, however enhanced availability of food resources may compensate for such potential effects.
4.2.3.6 Coho Salmon Table 4.2-3(8) presents the thermal evaluation data for coho salmon.
Evaluation of thermal effects data differs somewhat for this species from that of the other RIS discussed thus far.
Coho salmon are stocked in Lake Ontario as fingerlings and natural reproduction is presumed to be insignificant because of limited available streams with adequate water quality.
Reproduction would be expected to occur in streams during the fall.
Adults spawn only once and then die after spawning is completed.
Maximum for Survival During Reproductive Season Using the months of September and October to determine thermal effects, if any, on survival of adults near the Ginna discharge zone, the applicant finds a potential for exclusion from about 78 acres (extending lakeward about 2500 feet) of the surface discharge zone in September (assumes an ambient of 17.7 0 C (63.8 0 F).
In Octobez, coho could be theoretically excluded from an area 5.6 acres in size (extending lakeward about 900 feet).
Because of its vertical configuration, the discharge zone should not pose a barrier to coho migrating through the Ginna area.
Coho could pass under all but about 7 acres of the plume near the 4.2-39
bottom.
The area of thermal exclusion contains the previously discussed scour zone (maximum 5.2 acres).
Maximum for Summer Survival Coho salmon are reported to inhabit colder offshore waters near the thermocline in summer, and are not expected to encounter the discharge zone, or warm nearshore waters in general, at this time.
Optimum Growth The optimum growth temperature for juvenile coho salmon may be exceeded within about 58 percent (101.6 acres) of the surface discharge zone in June and October.
At the six foot depth region of the discharge zone, there is a potential for suboptimal growth within about 35 acres (20 percent of the discharge zone),
also restricted to June and October.
Acceptable Growth An acceptable growth temperature was calculated using criteria discussed in the 316(a) Guidance Manual (EPA, 1974).
The applicant's analysis demonstrates potential suboptimal growth of juveniles within a small area of 9.6 acres (surface) or 2.7 acres (six foot depths) during both June and October.
This assumes a continuous uninterrupted residence of coho within the discharge zone for about 30 days in June and October, an unlikely condition.
In all probability, residence time and the potential for impact will be of lesser magnitude.
4.2-40
Reproduction and Maximum for Development As previously mentioned, the season and temperatures for develop ment and reproduction are not applicable to this stocked species.
Potential for Cold Shock Coho salmon are excellent swimmers and may encounter the plume area during winter, spring, and fall; they normally avoid warm nearshore waters in summer.
For conservative predictive purposes, the applicant assumes coho can achieve acclimation to maximum plume temperatures in the cold months (note preference data in Table 3.3-4).
Spigarelli et. al.
(1974) report that coho, as well as other salmonids encountering thermal plumes, tend to acquire body temperatures somewhat less than discharge maximum, thus supporting the conservative nature of the applicant's approach and findings.
During warmer months coho are expected to inhabit waters near their thermal preferendum, which the applicant presumes to be a maximum 15.60C (60°F).
Lower lethal temperatures for coho (Table 4.2-4) were interpolated from data provided in Table 4.2-2(7).
The data suggest a potential for cold shock during winter months, assuming coho are present.
Howeve:-,
a paucity of coho in the applicant's winter fish studies suggests that the extent of impact, associated with a winter shut down, is expected to be extremely small.
No salmonids were observed in the discharge canal (region of maximum plume temperature) during two of the winter months monitored by a TV camera (January and 4.2-41
February) (RG&E, 1976b),
and no coho salmon were netted in the February 1975 gill net study (RG&E, 1976a).
These observations suggest the Ginna plume is not a strong attractant for coho during at least two, and presumably all three, of the critical winter months.
Summary In summary, the applicant's evaluation of theoretical thermal impact on coho salmon of Lake Ontario, has dem6nstrated a low potential for impact on mature forms migrating through the region beneath the discharge zone in late summer and October, and a minimum potential impact on acceptable growth of individuals occupying the discharge zone in spring and fall.
4.2.3.7 Brown Trout Table 4.2-3(9) presents the thermal evaluation data for brown trout.
The brown trout of Lake Ontario is another stocked species whose capability for natural reproduction along the south shore of Lake Ontario is questionable.
Maximum for Parental Survival Spawning has been recorded to occur primarily in October and November, though mature specimens may enter nearshore waters in September.
The sensitivity temperature for parental survival exceeds all temperatures within the Ginna discharge zone during October and November, thus eliminating potential impact during 4.2-42
the critical period.
There may be possible exclusion of brown trout from about 21 acres of the surface region, or 6 acres of the six foot depths, in September.
Maximum for Summer Survival Evaluation of potential impacts on brown trout in regard to summer survival, shows a potential exclusion from areas ranging from 60 acres (92 days) to 176 acres (18 days) within the surface waters of the discharge zone, and exclusion within about 20 acres (92 days) to 65 acres (18 days) at the six foot depths.
These represent conservative areas based on safe sensitivity temperatures (20 C or 3.60F below lethal temperatures).
Judging from the normal distri bution of brown trout in summer (see Section 3.3.9.2.1),
and their preference for offshore waters in the temperature range of 10-180 C (50-64.4 0 F),
it appears unlikely that many individuals would encounter the nearshore portions of the discharge zone in summer and be subject to a potential impact; note that ambient nearshore waters in summer (average 18.8 0 C and maximum 23.9 0 C) exceed preferred temperatures of brown trout.
In evaluating the data on optimum growth the same rationale as mentioned above applies.
Most brown trout are not expected to occupy nearshore waters in summer, thus minimizing the potential for impact on this activity.
For what few individuals might reside nearshore, there is a potential for suboptimal growth within 133 acres of the surface region and about 48 /acres of the six foot region.
During late spring (June) there is a potential for sub-4.2-43
optimal growth within a small area of 1.5 and 5.6 acres at the six foot depth and surface, respectively.
Acceptable Growth In reviewing the acceptable growth temperatures (Table 4.2-3(9))
a decrease in potential impact occurs for those few individuals residing near shore in summer.
There is no potential for thermal impact on acceptable growth in late spring (June), when ambient temperature (12.1 0 C or 53.7 F) is within the preferred range for brown trout.
Reproduction and Development As previously mentioned, the capability for stocked brown trout to reproduce along the southern shoreline of Lake Ontario is questionable.
Therefore the applicant assumes no potential for impact on reproduction and development.
Potential for Cold Shock Brown trout are also strong swimmers and have been observed in the Ginna discharge canal in fall.
Results of gill-net studies at Ginna indicate relatively low densities of brown trout near shore in spring, followed by an absence in July and August, and a maximum seasonal influx during the fall (note Table 3.3-6(7)).
A winter survey indicated considerably reduced concentrations relative to the fall period.
4.2-44
For conservative cold-shock evaluation purposes, the applicant will assume brown trout can acclimate to a maximum plume temper ature of 15.6 0 C (60 0 F) during cold months, and can thermoregulate to a preference temperature of 17.6 0 C (63.7 0 F, note Table 3.3-4) in warmer months, excluding July and August when they avoid near shore waters.
In the absence of definitive lower lethal temperatures for brown trout, it appears reasonable to approximate the data utilizing coho salmon data (Table 4. 2-2(7))since both species are cold-water members of the Salmonidae, and display similar upper thermal tolerances.
A comparison of lower lethal values and ambient temperatures (Table 4.2-4), indicates a potential for cold-shock effects only during the winter months.
This assumes a worst case acclimation to maximum plume temperatures; Spigarelli et al. (1974) found that salmonids do not necessarily acclimate to maximum discharge temper atures, but may thermoregulate to some intermediate elevated temper ature.
If browns acclimate to 10 0 C (50 0 F),
their lower lethal temperature would decline to about 1.90C (35.4°F),
and the potential for impact would likewise diminish.
The results of a February 1975 gill-net study at Ginna (RG&E, 1976a),
which yielded a total of only five brown trout among 152 m (500 feet) of experimental gill distributed between plume, near plume (E-0),
and control locations for 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br />, would indicate that a large brown trout population is not continually inhabiting the discharge area and thus suggests that the loss of brown trout following an unsche duled winter shutdown would not be measurable.
4.2-45
Summary In summary, the results of a theoretical impact assessment on brown trout at Ginna suggest no impact on mature specimens occupy ing nearshore waters in the fall, though there is a possible exclusion from a small area of the discharge zone should some individuals migrate shoreward earlier (September).
The potential for impact on growth (optimal and acceptable) is greatly minimized in summer since brown trout occupy waters somewhat offshore within their preferred temperature range.
No significant impact is predicted on growth in late spring (June); maximum exclusion area is 5.6 acres.
Reproduction and development of this stocked species is not expected to occur to any extent in Lake Ontario; therefore the applicant anticipates no potential for thermal impact on these activities.
4.2-46
LIST OF REFERENCES CHAPTER 4 Bell, M. C. 1973.
Fisheries handbook of engineering requirements and biological criteria.
U. S.
Army Corps of Engineers.
North Pacific Division.
Brett, J.
R. 1944.
Some lethal temperature relations of Algonquin Park fishes.
Univ. Toronto Series, Bio. Series #52, Publ. Ont.
Fish Res. Lab. 63: 1-49.
Brett, J.
R. 1952.
Temperature tolerance in young Pacific Salmon, Genus (Oncorhynchus).
J.
Fish. Bd. Can. 9: 265-323.
Carlander, K. D. 1970.
Handbook of Freshwater Fishery Biology, Volume I.
Iowa State University Press, Ames, Iowa.
Carter, W. A.
1887.
Temperature in relation to fish.
- Nature, London 36: 213-214.
Christianson, A.
G.,
and B.
A. Tichenor. 1968.
Industrial waste guide on thermal pollution.
Fed. Water Poll. Control Admin.
- Clemens, H. P.
1950.
Life cycle and ecology of Gammarus fasciatus.
Franz Theo. Stone Inst. Hydrobiology, Contrib. No.
12, Ohio State University.
Coble, D. W. 1975.
Smallmouth bass.
In:
Black Bass Biology and Management.
Sport Fishing Institute, Washington, D.C.,
- p. 21-33.
Colby, P.J.
1973.
Response of alewives (Alosa pseudoharengus),
to environmental change.
In: Walter Chavin (ed.), Responses of Fish to Environmental Changes..
C.C. Thomas, Springfield,III.
4.2-47
LIST OF REFERENCES (Cont'd)
CHAPTER 4 Coutant, C.
C.
1975.
Responses of bass to natural and artifical temperature regimes.
In:
Black Bass Biology and Management.
Sport Fishing Institute, Washington, D. C.,
- p. 272-285.
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.
- Embody, G. C.
1934.
Relation of temperature to incubation periods of eggs in four species of trout.
Trans. Amer. Fish. Soc. 64:
281-292.
Environmental Protection Agency.
1974.
316(a) Technical guidance thermal discharges.
Draft.
September 30, 1974.
Gray, J.
1928.
The effect of temperature on development of eggs of Salmo fario.
J.
Exp. Biol. 6: 125-130.
- Hale, J.
1960.
Some aspects of the life history of the smelt, Osmerus mordax, in Western Lake Superior.
Minn. Fish. Game.
Forest. Ser. 2: 25-41.
Klein, L.
1962.
River Pollution II.
Causes and effects in:
J.
R.
E.
Jone ed. Fish and River Pollution.
Butterworth, London.
pp. 254-310.
4.2-48
LIST OF REFERENCES (Cont'd)
CHAPTER 4
- Larimore, R.
W.,
and M. J.
Duever. 1968.
Effects of temperature acclimation on the swimming ability of smallmouth bass fry.
Trans. Amer. Fish. Soc. 97: 175-184.
- McErlean, A. J.,
and H. J.
Brinkley. 1971.
Temperature tolerance and thyroid activity of the white perch, Roccus morone americanus.
J.
Fish. Biol. 3: 97-114.
New York State Department of Environmental Conservation, 1975.
Fishing Lake Ontario for Salmon and trout. 10p.
National Academy of Sciences.
1973.
Water Quality Criteria -
1972.
EPA, Washington, D.C.
594 p.
- Otto, R.
G.,
M. A. Kitchel, and J.
- 0. Rice. 1976.
Lethal and preferred temperatures of the alewife (Alosa pseudoharengus) in Lake Michigan.
Trans. Am. Fish. Soc.,
1: 96-106.
Rochester Gas & Electric Corp.,
1976a.
Fish Net Study, February 25, 1975.
Ginna Nuclear Power Station.
Prepared by J.
F. Storr Ph.D.
, 1976b.
Visual Monitoring in the Discharge Canal.
Ginna N11clear Power Station, 1975.
Prepared by J.
F. Storr, Ph.D.
Ruetter, J.
M.,
and C.
E. Herdendorf. 1974.
Laboratory estimates of seasonal temperature preferences of Lake Erie fish species.
Federal Aid Project, F-41-R.
4.2-49
LIST OF REFERENCES (Cont'd)
CHAPTER 4 Scott, W. B.,
and E.
J.
Crossman. 1973.
Freshwater fishes of Canada.
Fish. Res. Bd. Can. Bull. 184, Ottawa.
Sheri, A.
N.
1968.
Growth dynamics of White perch, Roccus americanus, during colonization of the Bay of Quinte, Lake Ontario.
Univ. Waterloo, Ph.
D. Thesis, pp 366.
Sheri, A. N.,
and G. Power. 1968.
Reproduction of white perch, Roccus americanus, in the Bay of Quinte, Lake Ontario.
J. Fish.
Res. Bd. Can.
25(1): 2225-2231.
Spigarelli, S.
A.,
G. P.
- Romberg, W. Prepejchal, and M. M. Thommes.
1974.
Body-temperature characteristics of fish at a thermal dis charge on Lake Michigan.
In:
Thermal Fcology. p. 119-132.
Edited by J. Whitfield Gibbons and Rebecca R. Sharitz.
Technical Informa tion Center, U. S.
Atomic Energy Commission. CONF-730505.
- Sprague, J.
B.
1963.
Resistance of four freshwater crustaceans to lethal high temperature and low oxygen.
J. Fish. Res. Bd.
Can. 20(2): 387-415.
Storr, J.
F.,
and R. A. Sweeney.
1971.
Development of a theoreti cal seasonal growth response curve of Cladophora glomerata to light and temperature.
Proc. 14th Conf. Gr. Lakes Res.,
Int.
Assoc. Great Lakes Res.
Swift, A.
R. 1961.
The annual growth rate cycle in Brown trout.
Salmo trutta, and its cause.
J.
Exp. Biol. 38: 595-604.
4.2-50
LIST OF REFERENCES (Cont'd)
CHAPTER 4 Trembley, F.
J.
1961.
Research project on effects of condenser discharge water on aquatic life.
Project Report 1960.
Inst. of Res.,
Lehigh University.
U. S.
Department of the Interior. 1970.
Physical and ecological effects of waste heat on Lake Michigan.
Great Lakes Fishery Lab.,
Ann Arbor, Michigan, 101 p.
4.2-51
TABLE 4.2-1 AVERAGE MONTHLY AND SEASONAL INTAKE TEMPERATURES GINNA NUCLEAR POWER STATION Average Intake Temperature oc 0oF 1.6 34.9 0.9 33.7 1.5 34.7 Month Jan Feb Mar Apr May June July Aug Sept Oct Nov Dec 40.0 45.7 53.7 65.7 68.0 63.8 53.8 46.8 39.7 Season Winter Spring Summer 10% maximum*
5% maximum 1% maximum Fall Average Seasonal Temperature oC OF 1.3 8.1 18.8 21.1 22.2 23.9 8.2 34.4 46.5 65.8 70.0 72.0 75.0 46.8 NOTE:
- Temperature equal to or exceeded 10%,
5%,
or 1% of the year, whichever is appropriate.
4.4 7.6 12.1 18.7 20.0 17.7 12.1 8.2 4.3
TABLE 4.2-2 (1)
RIS TEMPERATURE DATA SHEET CLADOPHORA AND GAMMARUS I.
Lethal threshold:
Upper Cladophora Acclimation Temperature Juvenile Adult 26.1-32.2 0 C Gammarus
>26.0 0 C 31.0 C Data Source Storr & Sweeney,
- 1971, Observations in Ginna Discharge
- Sprague, 1963
- Clemens, 1950 II.
Growth:
Optimum and range Cladophora Gammarus III.
Reproduction:
Cladophora Gammarus Incubation and hatch Optimum n25.0°C Range 18.0OC 4.0-18.3'C
'x26.0°C <5.0->26.0°C
^,26.0 0 C <5.0->26.0Oc 18.0° C
- 20. OOC*
Month (s)
Spring, early summer, and fall Late March late October Storr & Sweeney, 1971 Clemens, 1950 Storr & Sweeney, 1971
- Clemens, 1950
- Clemens, 1950 NOTE:
Very conservative upper limit for optimal growth.
TABLE 4.2-2(2)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
Alewife (Alosa pseudoharengus)
I.
Lethal threshold:
Upper Lower Acclimation Temperature 16.5 C 16.5 0 C 16.3 0 C 10.0-12.0°C 18.0-20. 0C 24.0-26.0 C 10.0 15.0 20.0 27-2g 0 C 17.0 C II.
Growth:
Optimum and range II.
Reproduction:
Migration Spawning Incubation and hatch Larvae Juvenile 26.5 30.0 32.0 Optimum Range 22.80C 15.6-27.7°C
- 17. 80 C 13.0-27.0°C 6.9-29.40C 13.0-23.0°C Adult 27.5Oc***
(CTM) 28.5 0 C
- 27. 30C**
23.0 C 23-24.0 C 24-25.0 0 C]
33
- 09 7.0 C 22.7 C
>18.4 0 C Month(s)
April to early August Data Source Reutter & Herdendorf,
- 1974, P.
14
'I Otto et. al. 1976, Table 2
is of II Carlander, 1970, p.75 USDI, 1970 USDI, 1970 Carlander, 1970, P.
73 Christianson & Tichenor, 1968 Carlander, 1970, P.
74 Edsall, 1970, P.
378 (optimum)
Carlander, 1970, P.
74 (range)
Alive but stressed.
Lethality <50%.
TABLE 4.2-2(3)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
American Smelt (Osmerus mordax)
I.
Lethal threshold:
Upper Acclimation Temperature 6.0 0 C Not given Larvae Juvenile Adult (CTM) 24.9°C 21.5-28.50C Data Source Reutter & Herdendorf,
- 1974, P.
19, L. Erie Carlander, 1970, P.
314 (Marine specimens)
[I.
Growth:
Optimum and range
[I.
Reproduction:
Migration
>18.4 C Optimum Spawning Incubation and 8.30C hatch Range 0
8.9-18.3 C 2.2-14.5°C
- 8. 9-18. 30C 19-20 days at 5-8 0 C, 10 days at 15.0 0C 3.9-10.60C Month(s)
April to June, as late as July Carlander, 1970, P.
314 Bell, 1973, Chapter II, Table B Scott & Crossman,
- 1973, P.
314 Hale, 1960, L. Superior Scott & Crossman, 1973 Bell, 1973, Chapter II (optimum) Table D Carlander, 1970, P.
315 (range)
Lower
TABLE 4.2-2(4)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
Spottail Shiner (Notropis hudsonius)
I.
Lethal threshold:
Upper Lower Acclimation Temperature 7.2 0 C 6.0OC
- 5. 6°C
- 5. 8°C
- 10. 00C 2.9 0 C
- 12. 0°C 21.50C 14.0°C Larvae Juvenile Adult 30.60C (CTM) 27.60C (CTM)
(CTM)
(CTM)
- 27. 0°C 27.0 0°C 27.9 0 C
>13.9 0 C
< 1.6 °C
<11. 5oC*
< 3.0OC*
Data Source Trembley, 1961, P.
55 Reutter & Herdendorf,
- 1974, P.
18, L. Erie of Io
'I
'I Reutter & Herdendorf,
- 1974, P.
25, L. Erie It I,
i, I,
II.
Growth:
Optimum and range
- II.
Reproduction:
Migration Spawning Incubation and hatch Optimum Range 20.00C
>18.00 23.90C Month (s)
June-July Carlander, 1970, P.
426 Brett, 1944 Carlander, 1970, P.
426 Specimens alive at temperatures cited, therefore LD-50 is at some lower temperature.
TABLE 4.2-2 (5)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
White Perch I.
Lethal threshold:
Upper (Morone americana)
Acclimation Temperature 27.8 0 C Larvae 28.2 0 C 28.5 0 C 4.4 0 C 17.5°C 10.4 0 C 10.0 0 C
- 20. 30 C
- 28. 50 C 10.0°C Juvenile Adult 32.8°C 33.00 C 34.4 0 C
- 27. 80C 27.70C*
27.2OC*
26.20C*
29.2°C*
33.2°C
- 25. 20C Data Source McErlean & Brinkley,
- 1971, P.
102, estuarine it it I,
'U Christianson & Tichenor,
- 1968, P.
42 McErlean & Brinkley,
- 1971, P.
109, estuarine t!
I, WI I,
of I,
It It oI
'I II.
Growth:
Optimum and range rII.
Reproduction:
Migration Spawning 24.0 C Optimum 19.1°C Max 20.7 0 C Incubation and hatch Range 14.4-23. 0C 11.0-15.0 0 C Month (s)
Spring Mid May-June 15.0 0 C 15.0-20.0°C Scott & Crossman, 1973, P.
680 Sheri, 1968 Sheri & Power, 1968 Scott & Crossman, 1973, P.
686 LD-50
TABLE 4.2-2(6)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
Smallmouth Bass (Micropterus dolomieui)
I.
Lethal threshold:
Upper Lower Acclimation Temperature
- 12. 80 C
- 4. 80 C 4.80C 22.20C
- 24. 10C
- 12. 0°C 15.00C 18.00C
- 22. 0°C
- 26. 10C II.
Growth:
Optimum and range Larvae 32.8-35. 0°C Juvenile 32.8°C Adult 32.20C 16.0oC**
(CTM) 28.00C 3[o-***
32.2 35.2 *OC 1.0° C
- 2. 0°C 4.0Oc
- 7. 0°C 40 10.0°C 4°C (lower incipient) 28.0-29.0°C2 6 -2 9 0C
- 28. 30 C Data Source Kerr in Coble, 1975, P.
22 Trembley, 1960 Reutter & Herdendorf,
- 1974, P.
18 it I'
I' It II Reutter &
- 1974, P.
Horning &
- 1974, P.
'I Larimore & Duever, 1958, P.
183 Peak in EPA,
- 1974, P.
146 See summary by Coutant
- 1975, P.
276
- NAS, 1973 Herdendorf, 18 Pearson in
- EPA, 146 i,
No mortality after 56 hours6.481481e-4 days <br />0.0156 hours <br />9.259259e-5 weeks <br />2.1308e-5 months <br />.
Fish normal, no stress Fish died after brief period.
Sheet 1 of
TABLE 4.2-2(6) (Cont'd)
Range I I.
Reproduction:
Migration Spawning 17.0-18.0 C Incubation and hatch Month (s) 13.0-21.0 C May - July 15.0-18.0 C 12.8-26.1 0 C Data Source Breder & Rosen, in EPA 1974 (optimum)
Coutant (1975),
P.
273 If Sheet 2
TABLE 4.2-2(7)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
Coho Salmon (Oncorhynchus kisutch)
I.
Lethal threshold:
Upper Ldwer Acclimation Temperature 5.0°C
- 10. 00C 15.00°C 20.0°C 23.0°C 10.0 0 C
- 5. 0OC
- 10. 00C
- 15. 00C
- 20. 0°C
- 23. 0OC Larvae Juvenile 23.00 C
- 24. 0°C
- 24. 0°C
- 25. 0°C
- 25. 0°C Adult
- 21. 0°C 0.2 0 C 1.9 0C 3.5 0 C 5.0 0 C 6.0OC Data Source Brett, 1952, P.
301 It
'I it if Anonymous, in EPA 1974, P.
132 Brett, 1952, P.
301 it if
'I II.
Growth:
Optimum and range 15.0 0 C
- 5. 0-17. 00C II.
Reproduction:
Migration Spawning Incubation and hatch Optimum Range Month(s) 7.0-16.0°C
- 7. 0-13. 0°C Early Sept.
8.9-1O.7°C early Oct.
GLRL in EPA,
- 1974, P.
132 Averett in
- EPA, 1974, P.
132 Burrows, and anonymous in EPA, 1974, P.
132 Scott & Crossman, 1973, 161 It I
I
TABLE 4.2-2 (8)
TEMPERATURE DATA SHEET RIS FISH SPECIES:
Brown Trout (Salmo trutta)
I.
Lethal threshold:
Upper Acclimation Temperature 14.0-18.00C 26.0°oC 0
5.0-6.0°C Not given 20.0 C Not given Larvae 23.50C Juvenile 22.5 0 C 23.0 C II.
Growth:
Optimum and range Adult 25.0 C
- 26. 0°C 34.00F 18.3-23.90C 8.0-17.0 C 12.0-15.0°C Data Source Klein, 1962 It It Bishai in NAS,
- 1973, P.
160 Klein, 1962 Carter, 1887 Scott & Crossman,
- 1973, P.
199 Brett in
- NAS, 1973, P.
160 Swift, 1961, P.
598 III.
Reproduction:
Migration Spawning Optimum Incubation and hatch Range
- 6. 7-8. 90C 2.8-12.20C 1.9-11.2°C Month(s)
October November Scott & Crossman,
- 1973, P.
199 Gray, J., 1928 Embody, 1934
TABLE 4.2-3(1)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Cladophora 9lomerata' Biological Activity Considered Maximum for Survival of Parent Maximum for Summer Survival Optimum Growth Maximum for Development Normal Reproduction Dates and Temperature Time of Occurrence (Month or Season)
May June Summer 10% Maximum 5% Maximum October November Summer 10% Maximum 5% Maximum 1% Maximum May June Summer October November Temperature C (OF)
Isotherm Exceeding Ambient Sensitivity Sens. Temp.
7.6 12.1 18.8 21.1 22.2 12.1 8.2 18.8 21.1 22.2 23.9 7.6 12.1 18.8 12.1 8.2 (45.7)
(53.7)
(65.8)
(70.0)
(72.0)
(53.8)
(46.8)
(65.8)
(70.0)
(72.0)
(75.0)
(45.7)
(53.7)
(65.8)
(53.8)
(46.8) 22.2 22.2 22.2 22.2 22.2 22.2 22.2 32.2 32.2 32.2 32.2 18.0 18.0 18.0 18.0 18.0 (72.0)
(72.0)
(72.0)
(72.0)
(72.0)
(72.0)
(72.0)
(90.0)
(90.0)
(90.0)
(90.0)
(64.4)
(64.4)
(64.4)
(64.4)
(64.4) 10.1 (18.2) 3.4 (6.1) 1.1 (2.0) 10.1 (18.2) 10.0 (18.2) 8.3 (14.9) 10.4 (18.7) 5.9 (10.6) 5.9 (10.6) 9.8 (17.6)
Activity Excluded Percent of Surface Acres Discharge Zone 0
<5.1 6.5 10.7
<5.1 0
0 0
<5.1
<5.1
<5.1
<5.1
<5.1
<5.1 0
<2.9 3.7 6.1
<2.9 0
0 0
<2.9
<2.9
<2.9
<2.9
<2.9
<2.9 No.
of Days/Yr.
0 30 74 19 18 31 0
0 0
18 4
31 30 92 31 30 Data Source Storr &
Sweeney, 1971 Observations in Ginna Discharge Storr &
- Sweeney, 1971 Not applicable May June Summer October November 7.6 12.1 18.8 12.1 8.2 (45.7)
(53.7)
(65.8)
(53.8)
(46.8) 18.0 18.0 18.0 18.0 18.0 (64.4)
(64.4)
(64.4)
(64.4)
(64.4) 10.4 (18.7) 5.9 (10.6) 5.9 (10.6) 9.8 (17.6)
NOTE:
- No At exceeds sensitivity temperature at this time.
Ambient lake temperature is equal to or greater than sensitivity
- 1.
Evaluation for Cladophora based on bottom contact region.
<5.1
<5.1
<5.1
<5.1
<2.9
<2.9
<2.9
<2.9 31 30 92 31 30 Storr &
- Sweeney, 1971 temperature at this time.
TABLE 4.2-3(2)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Gammarus fasciatus Biological Activity Considered Maximum for Survival of Parent Maximum for Summer Survival Optimum Growth Time of Occurrence (Month or Season)
Spring Summer 10% Maximum 5% Maximum 1% Maximum October A
1 E & 12 1
A Summer 10% Maximum 5% Maximum 1% Maximum Summer 10% Maximum 5% Maximum 1% Maximum June Summer 10% Maximum October Temperature 0 C (OF)
Ambient Sensitivity 8.1 18.8 21.1 22.2 23.9 12.1 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 12.1 18.8 21.1 12.1 (46.5)
(65.8)
(70.0)
(72.0)
(75.0)
(53.8)
(65.8)
(/0.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(53.8)
(65.8)
(70.0)
(53.8) 28.2 31.0 31.0 31.0 31.0 29.0 29.7 31.0 31.0 31.0 26.0 26.0 26.0 26.0 20.0 20.0 20.0 20.0 (82.8)
(87.8)
(87.8)
(87.8)
(87.8)
(84.2)
(85.5)
(87.8)
(87.8)
(87.8)
(78.8)
(78.8)
(78.8)
(78.8)
(68.0)
(68.0)
(68.0)
(68.0)
Isotherm Exceeding Sens.
Temp.
9.9 (17.8) 8.8 (15.8) 7.1 (12.8) 9.9 (17.8) 8.8 (15.8) 7.1 (12.8) 7.2 4.9 3.8 2.1 (13.0)
(8.8)
(6.8)
(3.8) 7.9 (14.2) 1.2 (2.2) 7.9 (14.2)
Activity Excluded Percent of Surface Acres Discharge Zone 0
0
<5.1
<5. 1
<5.1 0
0
<5.1
<5.1
<5.1
<5.1
<5.1 5.1 9.3
<5.1 10.7
<5.1 0
0
<2.9
<2.9
<2.9 0
0
<2.9
<2.9
<2.9
<2.9
<2.9 2.9 5.3
<2.9 6.1
<2.9 No. of Days/Yr.
0 55 37 18 4
0 0
37 18 4
92 37 18 4
30 55 30 Data Source Sprague 1963,
- p.
401 & 408.
Sprague 1963,
- p. 401.
Clemens 1950,
- p.
35 Sheet 1
TABLE 4.2-3(2) (Cont'd)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Gammarus fasciatus Biological Activity Considered Optimum Growth 13 Maximum for Development, Reproduction Dates and Temperatures Time of Odcurrence (Month or Season)
Summer 10% Maximum 5% Maximum 1% Maximum Summer 10% Maximum 5% Maximum 1% Maximum Temperature °C (OF)
Isotherm Exceeding Ambient Sensitivity Sens.
Temp.
18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0) 25.0 25.0 25.0 25.0 26.0 26.0 26.0 26.0 (77.0)
(77.0)
(77.0)
(77.0) 6.2 3.9 2.8 1.1 7.2 4.9 3.8 2.1 (11.2)
(7.0)
(5.0)
(2.0)
(13.0)
(8.8)
(6.8)
(3.8)
Activity Excluded Percent of Surface Acres Discharge Zone
<5.1 5.1 7.9 10.7
<5.1
<5.1 5.1 9.3
<2.9 2.9 4.5 6.1
<2.9
<2.9 2.9 5.3 No.
of Days/Yr.
92 37 18 4
92 37 18 4
No At exceeds sensitivity temperature at this time.
Ambient lake temperature is equal to or greater than sensitivity temperature at this time.
- Adults,
- 2.
Eggs and Immatures,
- 3.
Immatures.
Data Source Clemens 1950,
- p.
35 Clemens 1950,
- p.
52 NOTE:
1.
Sheet 2
TABLE 4.2-3(3)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Alewife (Alosa pseudoharen Biological Activity Considered Maximum for Survival of Parent Time of Occurrence (Month or Season)
Spring June July 6'
June 6' July Summer 10% Maximum 5% Maximum 1% Maximum Maximum for Summer Survival 1 Optimum Growth 6'
6' 6'
6' Summer 10% Maximum 5% Maximum 1% Maximum June Summer 10% Maximum October 6' June 6'
Summer 6'
10% Maximum 6' October gus)o a
Temperature 0 C (F)
Isotherm Exceeding Ambient Sensitivity Sens. Temp.
8.1 12.1 18.7 12.1 18.7 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 12.1 18.8 21.1 12.1 12.1 18.8 21.1 12.1 (46.5)
(53.7)
(65.7)
(53.7)
(65.7)
(65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(53.7)
(65.8)
(70.0)
(53.8)
(53.7)
(65.8)
(70.0)
(53.8) 22.0 (71.6) 23.0 (73.4) 28.0 (82.4) 28.0 (82.4) 29.0 (84.2) 30.0 (86.0) 28.0 (82.4) 28.0 (82.4) 29.0 (84.2) 30.0 (86.0) 22.7 (72.9)
H 4.3 (7.7) 4.3 (7.7) 9.2 6.9 6.8 6.1 9.2 6.9 6.8 6.1 10.6 3.9 1.6 10.6 10.6 3.9 1.6 10.6 (16.6)
(12.4)
(12.2)
(11.0)
(16.6)
(12.4)
(12.2)
(11.0)
(19.1)
(7.0)
(2.9)
(19.1)
(19.1)
(7.0)
(2.9)
(19.1)
Acres 0
0 59.7 0
19.4 5.6 16.1 16.1 20.9 1.5 4.6 4.6 6.1 2.3 59.7 175.7 2.3 0.7 19.4 64.9 0.7 Activity Excluded Percent of Surface Discharge Zone 0
0 34.0 0
11.0 3.2 9.2 9.2 11.9 0.9 2.6 2.6 3.5 1.3 34.0 100.0 1.3 0.4 11.0 36.9 0.4 No. of Days/Yr.
0 0
15 0
15 92 37 18 4
92 37 18 4
30 92 37 31 30 92 37 31 Data Source Table 4.2-2(2)
Table 4.2-2(2)
Table 4.2-2(2)
Sheet 1
TABLE 4.2-3(3) (Cont'd)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Alewife (Alosa pseudoharengi Biological Activity Considered Acceptable Growth Time of Occurrence (Month or Season)
Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' Maximum for Development Normal Reproduction Dates and Temperatures Summer 10% Maximum 5% Maximum 1% Maximum Spring July Spring July us)
Temperature 0C (OF)
Isotherm Exceeding Ambient Sensitivity Sens. Temp.
18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0) 26.8 (80.2)
H H
SI 8.1 (46.5) 29.4 (84.9) 18.7 (65.7) 8.1 (46.5) 27.7 (81.9) 18.7 (65.7) 8.0 5.7 4.6 2.9 8.0 5.7 4.6 2.9 (14.4)
(10.3)
(8.3)
(5.2)
(14.4)
(10.3)
(8.3)
(5.2) 9.0 (16.2)
Activity Excluded Percent of Surface Acres Discharge Zone 9.6 27.1 45.8 101.6 2.7 8.2 14.5 35.2 0
0 0
5.6 5.5 15.4 26.1
- 57.8 1.5 4.7 8.3 20.0 0
0 0
3.2 No.
of Days/Yr.
92 37 18 4
92 37 18 4
0 0
0 31 NOTE:
No At exceeds sensitivity temperature at this time.
I. For juveniles.
Sheet 2 Data Source Table 4.2-2(2)
Table 4.2-2(2)
Table 4.2-2(2)
SPECIES:
American Smelt (Osmerus morc Biological Activity Considered Maximum for Survival of Parent Time of Occurrence (Month or Season)
April-May TABLE 4.2-3(4)
EVALUATION OF THERMAL DATA FOR RIS dax)
Temperature °c (OF)
Isotherm Exceeding Ambient Sensitivity Sens.
Temp.
6.0 (42.8) 18.3 (64.9)
Acres 0
Activity Excluded Percent of Surface Discharge Zone 0
No.
of Days/Yr.
0 Data Source Table 4.2-2(3) 55 Carlander 1970, p. 314 Summer 10% Maximum 5% Maximum 1% Maximum Maximum for I
Summer Survival 6'
6' 6'
6' Summer 10% Maximum 5% Maximum 1% Maximum Optimum Juveniles Summer Growth Adults Summer Maximum for Development Normal Reproduction Dates and Temperature Spring (Bottom)
Winter Spring Summer (Bottom)
(Bottom)
(Bottom) 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0) 21.0 (69.8) n N
N 18.8 (65.8) >18.4 (65.1) 18.8 (65.8) <10.6 (51.1) 8.1 (46.5) 15.0 (59.0) 1.3 8.1 18.8 (34.4)
(46.5)
(65.8) 14.5 (58.1) of 2.2 (4.0) e0 I'
2.2 (4.0) 6.9 (12.4) 6.4 (11.5) 133.2 47.6
<5.1 0
<5.1 75.8 27.1
<2.9 0
<2.9 55 91 0
91 Table 4.2-2(3)
Table 4.2-2(3)
Table 4.2-2(3)
NOTE:
- 1.
Only juveniles subject to impact at this time.
No At exceeds sensitivity temperature at this time.
Ambient lake temperature is equal to or greater than sensitivity temperature.
TABLE 4.2-3(5)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Spottail Shiner (Notropis hudsonius)
Biological Activity Considered Maximum for Survival of Parent Maximum for Summer Survival Time of Occurrence (Month or Season)
Ambient June July 12.1 (53.7) 18.7 (65.7)
Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' Optimum Growth Summer 10% Maximum 5% Maximum 1% Maximum Summer 10% Maximum 5% Maximum 1% Maximum 61 6'
6' 6'
Summer 10% Maximum 5% Maximum 1% Maximum 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
Temperature °C (OF)
Sensitivity Isotherm Exceeding Sens.
Temp.
28.6 (83.5) 28.6 (83.5) 9.9 (17.8) 28.6 (83.5)
N N
9.8 7.5 6.4 4.7 "9.8 "N
7.5 6.4 "t
4.7 23.9 (75.0) 5.1 "to 2.8 "1.7 "to 5.1 "to 2.8 "1.7 N
(17.6)
(13.5)
(11.5)
(8.5)
(17.6)
(13.5)
(11.5)
(8.5)
(9.2)
(5.0)
(3.0)
(9.2)
(5.0)
(3.0)
Activity Excluded Percent of Surface Acres Discharge Zone 0
4.3 4.3 12.4 20.9 45.8 1.2 3.5 6.1 14.5 35.2 101.6 175.7 10.9 35.2 64.9 0
2.4 2.4 7.1 11.9 26.1 0.7 2.0 3.5 8.3 20.0 57.8 100.0 6.2 20.0 36.9 No.
of Days/Yr.
0 31 92 37 18 4
92 37 18 4
92 37 18 4
92 37 18 4
Data Source Table 4.2-2(4)
Table 4.2-2(4)
Table 4.2-2(4)
Sheet 1
TABLE 4.2-3(5)(Cont'd)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Spottail Shiner (Notropis hudsonius)
Biological Activity Considered Acceptable Growth Maximum for Development Normal Reproduction Dates And Temperature Time of Occurrence (Month or Season)
Summer 10% Maximum 5% Maximum 1% Maximum 6'
Summer 6'
10% Maximum 6'
5% Maximum 6'
1% Maximum June -
July (Avg.)
(Bottom)
June - July (Avg.)
(Bottom)
Temperature 0C (0 Isotherm Exceeding Ambient Sensitivity Sens. Temp.
18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0) 15.4 (59.7) 15.4 (59.7) 26.1 (79.0)
H H
H H
20.0 (68.0) 20.0 (68.0) 7.3 (13.1) 5.0 (9.0) 3.9 (7.0) 2.2 (4.0) 7.3 (13.1) 5.0 (9.0) 3.9 (7.0) 2.2 (4.0) 4.6 (8.3) 4.6 (8.3)
Acres 12.4 35.2 59.7 133.2 3.5 10.9 19.4 47.6
<5.1
<5.1 Activity Excluded Percent of Surface Discharge Zone 7.1 20.0 34.0 75.8 2.0 6.2 11.0 27.1
<2.9
<2.9 No. of Days/Yr.
92 37 18 4 92 37 18 4
61 61 NOTE:
No At exceeds sensitivity temperature at this time.
Ambient lake temperature is equal to or greater than sensitivity temperature.
Sheet 2 Data Source Table 4.2-2(4)
Table 4.2-2(4)
Table 4.2-2(4)
TABLE 4.2-3(6)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
White Perch (Morone americana)
Biological Activity Considered Maximum for Survival of Parent Maximum for Summer Survival Temperature 0 C (OF)
Time of Occurrence (Month or Season)
Ambient Spring 8.1 (46.5)
Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' Optimum Growth Summer 10% Maximum 5% Maximum 1% Maximum June Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' 6'
June Summer 10% Maximum 5% Maximum 1% Maximum 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 12.1 18.8 21.1 22.2 23.9 12.1 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(53.7)
(65.8)
(70.0)
(72.0)
(75.0)
(53.7)
(65.8)
(70.0)
(72.0)
(75.0)
Sensitivity 28.0 (82.4) 29.6 29.9 30.0 30.3 29.6 29.9 30.0 30.3 (85.3)
(85.8)
(86.0)
(86.5)
(85.3)
(85.8)
(86.0)
(86.5) 24.0 (75.2)
- 1 Isotherm Exceeding Sens.
Temp.
8.8 (15.8) 7.8 (14.0) 6.4 (11.5) 8.8 (15.8) 7.8 (14.0) 6.4 (11.5) 5.2 (9.4) 2.9 (5.2) 1.8 (3.2) 5.2 (9.4) 2.9 (5.2) 1.8 (3.2)
Activity Excluded Percent of Surface Acres Discharge Zone 0
0 0
5.6 9.6 20.9 0
1.5 2.7 6.1 0
3.2 5.5 11.9 0
0.9 1.5 3.5 0
20.0 57.8 100.0 0
6.2 20.0 36.9 0
35.2 101.6 175.7 0
10.9 35.2 64.9 No.
of Days/Yr.
0 0
37 18 4
0 37 18 4
0 92 37 18 0
92 37 18 Data Source Table 4.2-2(5)
Table 4.2-2(5)
Table 4.2-2(5)
Sheet 1
!1 tt
TABLE 4.2-3(6) (Cont'd)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
White Perch (Morone americana)
Biological Activity Considered Acceptable Growth Time of Occurrence (Month or Season)
Amb June Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' 6'
Maximum for Development Normal Reproduction Dates and Temperature June Summer 10% Maximum 5% Maximum 1% Maximum Bottom June 12.1 18.8 21.1 22.2 23.9 12.1 18.8 21.1 22.2 23.9 Temperature 0C (0 Isotherm Exceeding ient Sensitivity Sens. Temp.
(53.7)
(65.8)
(70.0)
(72.0)
(75.0)
(53.7)
(65.8)
(70.0)
(72.0)
(75.0) 27.5 (81.5)
'U
'I NI H
H 12.1 (53.7) 20.0 (68.0)
Bottom Mid-May-June 9.9 (49.8) 15.0 (59.0) 8.7 (15.7) 6.4 (11.5) 5.3 (9.5) 3.6 (6.5) 8.7 (15.7) 6.4 (11.5) 5.3 (9.5) 3.6 (6.5) 7.9 (14.2) 5.1 (9.2)
Activity Excluded Percent of Surface Acres Discharge Zone 0
7.4 20.9 35.2 77.8 0
2.0 6.1 10.9 26.1
<5.1
<5.1 0
4.2 11.9 20.0 44.3 0
1.1 3.5 6.2 14.9
<2.9
<2.9 No.
of Days/Yr.
0 92 37 18 4 0
92 37 18 4
30 30 NOTE:
No At exceeds sensitivity temperature at this time.
Ambient lake temperature is equal to or greater than sensitivity temperature.
Sheet 2 Data Source Table 4.2-2(5)
Table 4.2-2(5)
Table 4.2-2 (5)
TABLE 4.2-3(7)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Smallmouth Bass (Micropterus dolomieui)
Temperature °C (OF)
Biological Isotherm Activity Time of Occurrence Exceeding Considered (Month or Season)
Ambient Sensitivity Sens.
Temp.
Maximum for Survival of Parent Maximum for Summer Survival Spring July 8.1 (46.5) 20.7 (69.3) 18.7 (65.7) 28.4 (83.1)
Summer 10% Maximum 5% Maximum 1% Maximum 6l 6'
6' 6'
Summer 10% Maximum 5% Maximum 1% Maximum Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' Summer 10% Maximum 5% Maximum 1% Maximum 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0) 28.5 30.5 31.5 33.2 28.5 30.5 31.5 33.2 (83.3)
(86.9)
(88.7)
(91.8)
(83.3)
(86.9)
(88.7)
(91.8) 28.3 (82.9) n
'I 9.7 (17.5) 9.7 9.4 9.3 9.3 9.7 9.4 9.3 9.3 9.5 7.2 6.1 4.4 9.5 7.2 6.1 4.4 (17.5)
(16.9)
(16.7)
(16.7)
(17.5)
(16.9)
(16.7)
(16.7)
(17.1)
(13.0)
(11.0)
(7.9)
(17.1)
(13.0)
(11.0)
(7.9)
Activity Excluded Percent of Surface Acres Discharge Zone 0
4.3 4.3 4.3 5.6 5.6 1.2 1.2 1.5 1.5 4.3 12.4 20.9 45.8 1.2 3.5 6.1 14.5 0
2.4 2.4 2.4 3.2 3.2 0.7 0.7 0.9 0.9 2.4 7.1 11.9 26.1 0.7 2.0 3.5 8.3 No.
of Days/Yr.
0 15 92 37 18 4
92 37 18 4
92 37 18 4
92 37 18 4
Optimum Growth Data Source Table 4.2-2(6)
Table 4.2-2(6)
Table 4.2-2(6)
Sheet I
TABLE 4.2-3(7) (Cont'd)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Smallmouth Bass (Micropterus dolomieui)
Biological Temperature °C (O)
Isotherm Activity Time of Occurrence Exceeding Considered (Month or Season)
Ambient Sensitivity Sens.
Temp.
Acceptable Growth Maximum for Development Normal Reproduction Dates and Temperatures Summer 10% Maximum 5% Maximum 1% Maximum 6'
Summer 6'
10% Maximum 6'
5% Maximum 6'
1% Maximum m) Spring m) Summer m) 10% Maximum m) 5% Maximum m) 1% Maximum (Btm) May (Btm) June (Btm) July 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 8.1 18.8 21.1 22.2 23.9 7.6 12.1 18.7 (65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0)
(46.5)
(65.8)
(70.0)
(72.0)
(75.0)
(45.7)
(53.7)
(65.7) 30.6 (87.1)
It of 29.0 (84.2) to 21.0 (69.8)
It to 9.5 (17.1) 8.4 (15.1) 6.7 (12.1) 9.5 (17.1) 8.4 (15.1) 6.7 (12.1) 10.2 7.9 6.8 5.1 (18.4)
(14.2)
(12.2)
(9.2) 8.9 (16.0) 2.3 (4.1)
Activity Excluded Percent of Surface Acres Discharge Zone 0
4.3 7.4 16.1 0
1.2 2.0 4.6
<5.1 It 0
<5.1 9.3 0
2.4 4.2 9.2 0
0.7 1.1 2.6
<2.9 it of 0
<2.9 5.3 No.
of Days/Yr.
0 37 18 4 0
37 18 4
92 37 18 4
0 30 31 NOTE:
- No At exceeds the sensitivity temperature.
Sheet 2 (Btr (Btr (Btr (Bti (Bti Data Source Table 4.2-2(6)
Table 4.2-2(6)
Table 4.2-2(6)
TABLE 4.2-3(8)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Coho Biological Activity Considered Maximum for Survival of Parent Maximum for Summer Survival Optimum Growth Salmon (Oncorhynchus kisutch)
T Temperature CC (OF)
Isotherm Time of Occurrence Exceeding (Month or Season)
Ambient Sensitivity Sens.
Temp.
Acres September October 17.7 (63.8) 21.0 (69.8) 12.1 (53.8) 21.0 (69.8) 3.3 (5.9) 8.9 (16.0) 77.8 5.6 Activity Excluded Percent of Surface Discharge Zone 44.3 3.2 No. of Days/Yr.
30 31 Coho salmon reside offshore near the thermocline in summer.
June Summer October 6' June 6'
Summer 6' October Acceptable Growth June Summer October 6' June 6'
Summer 6'
October Maximum for Development and Reproduction Dates and Temperatures 12.1 18.8 12.1 12.1 18.8 12.1 12.1
- 18. 8 12.1 12.1 18.8 12.1 (53.7) 15.0 (59.0)
(65.8)
(53.7)
(53.7)
(65.8)
(53.7)
It It (53.7) 20.0 (68.0)
(65.8)
(53.7)
(53.7)
(65.8)
(53.7)
U'
'S 2.9 (5.2) 2.9 (5.2) 2.9 (5.2) 2.9 (5.2) 2.9 (5.2) 7.9 (14.2) 7.9 (14.2) 7.9 (14.2) 7.9 (14.2) 101.6 101.6 35.2 35.2 9.6 9.6 2.7 2.7 57.8 57.8 20.0 20.0 5.5 5.5 30 31 30 31 30 31 30 31 1.5 1.5 Not applicable - stocked species.
Spawning occurs in streams, not in the lake.
Data Source Table 4.2-2(7)
NYSDEC, 1975 Table 4.2-2(7)
Table 4.2-2(7)
- NYSDEC, 1975 NOTE-Ambient lake temperature exceeds sensitivity temperature.
TABLE 4.2-3(9)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Brown Trout (Salmo trutta)
Biological Activity Considered Maximum for Survival of Parent Maximum for Summer Survival Time of Occurrence (Month or Season)
September October November Summer 10% Maximum 5% Maximum 1% Maximum 6'
6' 6'
6' Optimum Growth Summer 10% Maximum 5% Maximum 1% Maximum June Summer 10% Maximum 6'
June 6'
Summer 6'
10% Maximum Temperature 0 C (IF)
Isotherm Exceeding Ambient Sensitivity Sens.
Temp.
17.7 12.1 8.2 18.8 21.1 22.2 23.9 18.8 21.1 22.2 23.9 12.1 18.8 21.1 (63.8)
(53.8)
(46.8)
(65.8)
(70.0)
(72.0)
(75.0)
(65.8)
(70.0)
(72.0)
(75.0 (53.7)
(65.8)
(70.0) 12.1 (53.7) 18.8 (65.8) 21.1 (70.0) 24.0 24.0 24.0 23.0 23.6 23.7 23.7 23.0 23.6 23.7 23.7 (75.2)
(75.2)
(75.2)
(73.4)
(74.5)
(74.7)
(74.7)
(73.4)
(74.5)
(74.7)
(74.7) 21.1 (70.0)
'I H
6.3 (11.3) 4.2 (7.6) 2.5 (4.5) 1.5 (2.7) 4.2 (7.6) 2.5 (4.5) 1.5 (2.7) 9.0 (16.2) 2.3 (4.1) 9.0 (16.2) 2.3 (4.1)
Acres 20.9 0
0 59.7 133.2 175.7 19.4 47.6 64.9 5.6 133.2 1.5 47.6 Activity Excluded Percent of Surface Discharge Zone 11.9 0
0 34.0 75.8 100.0 11.0 27.1 36.9 3.2 75.8 0.9 27.1 No.
of Days/Yr.
30 0
0 92 37 14 92 37 14 30 55 30 55 Data Source Table 4.2-2(8)
Table 4.2-2(8)
Table 4.2-2 (8)
Sheet I
TABLE 4.2-3(9) (Cont'd)
EVALUATION OF THERMAL DATA FOR RIS SPECIES:
Brown Trout (Salmo trutta)
Biological Activity Considered Acceptable Growth Maximum for Development and Reproduction Dates and Temperatures Time of Occurrence (Month or Season)
Amb June Summer 10% Maximum 6' June 6'
Summer 6'
10% Maximum 12.1 18.8 21.1 12.1 18.8 21.1 Temperature 0 C (OF)
Isotherm Exceeding
)ent Sensitivity Sens. Temp.
(53.7)
(65.8)
(70.0)
(53.7)
(65.8)
(70.0) 22.7 (72.9) 6n 3.9 (7.0) 1.6 (2.9) 3.9 (7.0) 1.6 (2.9)
Acres 0
59.7 175.7 0
19.4 64.9 Activity Excluded Percent of Surface Discharge Zone 0
34.0 100.0 0
11.0 36.9 No.
of Days/Yr.
0 92 37 Data Source Table 4.2-2(8) 0 92 37 Not applicable - stocked species.
Spawning expected in streams, not in the lake.
NOTE:
No At exceeds the sensitivity temperature.
Ambient lake temperature is equal to, or exceeds, sensitivity temperature.
shppt 7 I
TABLE 4.2-4 LOWER THERMAL TOLERANCE OF RIS FISH AS RELATED TO DISCHARGE AND AMBIENT WATER TEMPERATURES 0C ( F) kverage Monthly
)ischarge Temp.
kverage Monthly
%mbient Temp.
Winter Jan Feb Mar 15.6 15.6 15.6 (60.0) (60.0) (60.0) 1.6 0.9 1.5 (34.9)
(33.7) (34.7)
Spring Apr May June 15.6 18.7 23.2 (60.0) (65.7) (73.7) 4.4 7.6 12.1 (40.0) (45.7) (53.7)
Summer July Aug Se-p 29.8 31.1 28.8 (85.7)
(88.0) (83.8) 18.7 20.0 17.7 (65.7)
(68.0) (63.8)
.ower Lethal Temperature for RIS Alewife Smelt NA NA NA 6.2 7.2 8.7 (43.2) (45.0) (47.7)
(41.5)
Spottail Shiner
<1.
(34.*
White Perch
- 0.
(33.
Smallmouth Bass NA Coho Salmon Brown Trout Note:
t 5.3)
(41.5)
(41.5) 6
<1.
<1.6
- 9) (34.9) (34.9) 9 N0.90 N0.9
- 6) (33.6)
(33.6)
.0 3.7 (38.7)
(38.7)
- 5. 3 6.9 9.1 (41.5)
(44.4)
(48.4) 3.3 3.3 8.7 (37.9)
(37.9) (47.7)
'0.9 3.8 6.1 (33.6)
(38.8) (43.0)
NA NA 2.5 5.3 8.1 (36.5)
(41.5) (46.6) 3.7 3
(3.7 (38.7) (38.7) 3.ý 3.P (38.7) (38.7) 3.7 3.7 3.7 (38.7) (38.7)
(38.7) 3.7 4.1 4.1 (38.7)
(39.4)
(39.4)
(48.7)
(48.7) 9.4J0 (48.7)
Fall Oct Nov Dec 23.2 19.3 (73.8) (66.8) 12.1 8.2 (53.8) (46.8) 8.7 7.4 (47.7) (45.3)
NA NA NA 9.1 7.2 (48.4) (45.0) 8.7 8.7 8.7 (47.7)
(47.7) (47.7) 9.4 10.0 8.9 (48.9)
(50.0) (48.0) 13.9 14.4 12.4 (57.0)
(57.9) (54.3) 8.7 3.3 (47.7) (37.9) 6.1 4.1 (43.0) (39.4) 8.1 5.8 (46.6) (42.4)
NA NA NA 3.7 3.7 (38.7) (38.7)
NA NA 4.1 4.1 3.7 (39.4)
(39.4) (38.7)
Data Basis and Comments 15.6 (60.0) 4.3 (39.7) 6.20interpolated from LD50,s (43.2) in Table 4.2-2(2) 5.30 EPA(1974)nomograph, (41.5) acclimation to maximum discharge 3.3 these values exceed LD50,s (37.9) see Table 4.2-2(4)
-0.9 EPA(1974)nomograph and (33.6) other (see Section 5.4.4L acclimation to ambient+5uC 2.5 interpolated from Table (36.5) 4.2-2(6) 3.7 acclimation does not ex (38.7) ceed 15.6 0 C,lower lethal based on Table 4.2-2(7) 3.7 (38.7) based on coho data Table 4.2-2 (7)
A = NOt Applicable at this time because most of the population is located offshore and not subject to plume influence.
- = Lower lethal temperature exceeds average monthly ambient temperature, thus signifying a potential for cold shock.
- 1. Variously based assuming acclimation to either maximum discharge temperature, preference temperature, or some other value associated with plume penetration; see text, Section 4.2, for a complete account and evaluation.
- 2.
Based on summer preference temperature of 25 0 C for juveniles; adults will be offshore by mid-August.
30(86) w S25(77) 120(68)
I, 15(59) o 10(51)
(E (L 5(41) 0(32) 5(41) 10(50)
AMBIENT TEMPERATURE 15(59)
NOMOGRAPH TO DETERMINE THE MAXIMUM WEEKLY AVERAGE TEMPERATURE OF PLUMES FOR VARIOUS AMBIENT TEMPERATURES °C (0F)
RmI NC E
LUPGSADlCTRic TIHE STERLING POWER PROJECT FIGURE 4.2-1
TABLE OF CONTENTS CHAPTER 5:
ASSESSMENT OF ADDITION4AL PLUME EFFECTS Page PLUME ENTRAINMENT............................
5.1-1 5.1.1 Hydrological Discussion......................
5.1-1 5.1.2 Biological Assessment........................
5.1-6 EFFECTS ON FISH MIGRATION..........................
5.2-1 POTENTIAL FOR GAS BUBBLE rISFESF.......
5.3-1 5-i Section 5.1 5.2 5.3
LIST OF TABLES TABLE NUMBER TITLE 5.1-1 Ambient and Entraining Water Flow Rates 5.1-2 Projected Plume Entrainment of Ichthyoplankton and Macroinvertebrates 5.1-3 Projected Plume Entrainment of Ichthyoplankton and Macroinvertebrates 5.1-4 Projected Plume Entrainment Assuming Various Levels of Countercurrent Mixing 5-ii
LIST OF FIGURES TITLE Isothermal Flow Rates-Expected Spring Conditions Isothermal Flow Rates-Extreme Spring Conditions 5-iii FIGURE NUMBER 5.1-1 5.1-2
5.1 PLUE ENTRAI*z 5.1.1 HYDROLOGICAL DISCUSSION The flow rate within any vertical plume cross section can be calculated from a knowledge of the discharge characteristics and the temperature and velocity distributions.
Since virtually all of the temperature decay in the near field plume is a result of mixing with the ambient, the local temperature excess also tells one the ratio of total flow to discharge flow.
That is, AT0 D =-
=Q-(1)
AT d
where D
= average dilution in cross section AT
= discharge excess temperature AT
average cross sectional excess temperature S
total plume flow rate through cross section (d = discharge flow rate The portion of the flow that is water entrained by the plume can be calculated from, e = Q - Q (2) where Oe = portion of plume flow rate throuqh cross section which is entrained water.
5.1-1
The average temperature in a plume cross section can be found by assuming that the pltme excess velocity has the same lateral distribution as the excess temperature, where the lateral excess temperature distribution is given by:
AT= AT exp
-L (3) where r
= lateral distance from the centerline AT
= centerline excess temperature c
AT
= excess temperature at lateral distance r from centerline a
= Gaussian standard deviation rh
= plume half width (see Section 1.4.1.1.4.4).
The average teperature in any horizontal plane is then:
f U exp 2 J&C exp(
2/d AT 2a 27 ATC (4) fcU exp (A2dr N
where Uc = excess centerline velocity.
Note that Uc is not present in the result and, therefore, no assumption need be made of its value.
Substituting equation 4 into equation 1 yields:
5.1-2
Ot = d (
ATO ATO and Qd are known frm the discharge conditions and ATc of distance along the plume centerline, can be found by the in Section 1.4.
Therefore, t is determined.
The fraction of the total flow within a lateral distance of plume centerline can be found from:
, as a function methods given
+/-Rfram. the FRf2 2Q (6) where:
FR = fraction of plume flow within +/- R of the centerline R = distance fran centerline Substituting R for r in equation 3, solving for R, and substituting the result in equation 6 yields:
FAT = erfnTC (7)
FAT = fraction of plume flow with excess tempera ture greater than AT 5.1-3 (5) where
Equations 5 and 7 were used to estimate the flow as a function of temperature and distance along the plume centerline.
Plume depth was assumed to vary fran 10 feet at the end of the zone of flow establishment to six feet at the point where T = 0 in equation 41 of Section 1.4 to zero feet at the point where T = 0 in equation 38 of Section 1.4.
Figure 5.1-1 shows the plume flow versus temperature and centerline distance for the expected spring conditions of Section 1.4.2.5.
The plume flow exposed to excess temperatures of 3°F or higher is seen to reach a maxinum of 3300 cfs at approxiamtely 2000 feet along the plume's trajectory.
This represents 69% of the total plume flow of 4800 cfs at this point.
The discharge flow is 891.2 cfs.
This reans the entrainment flow at this point is apprcximately 3910 cfs, 81% of the total flow.
Applying this same percentage to the 30F flow yields approximately 2690 cfs of entrain6d water exposed to 3°F temperatures or higher at a distance of 2000 feet along the plume centerline.
Figure 5.1-2 shows the plume flow versus teerature and centerline distance for the extreme spring conditions of Section 1.4.2.5.
The maximn 3°F flow is 3700 cfs at 5500 feet along the plume centerline.
The total plume flow at this point is 7300 cfs, 88% of which is entrained water.
The 30 F flow at this point can therefore be estimated as consisting of 88% entrained water, or apprcximtely 3250 cfs.
Of special note is the behavior of the total plume flow curves in Figures 5.1-1 and 2.
According to equation 1, the total plume flow approaches infinity as the plume excess temperature approaches zero.
This is the behavior indicated in the figures. Realistically, however, when the excess terperature of the plume is small, the plume water is indistinguishable fran the ambient.
Under such conditions it would be nore correct, fran the standpoint of impact assessment, to consider the plume flow as decreasing with snaller excess temperatures.
It therefore follows that the use of the total plume flow of Figures 5.1-1 and 2 for impact assess rent purposes is misleading for small excess temperatures.
A more realistic approach would be to consider the flow within a given isotherm, 5.1-4
say 39F, as the plume flow. All water outside of this isotherm can, for practical purposes, be identified as ambient water.
Table 5.1-1 gives 39F entraining water flow rates for expected and extreme spring conditions.
Also included are natural lake flows based on a cross current of 0.2 fps, a normal value for the site.
It can be seen that the expected and extreme spring 30F entrainent flows are greater than the lake flows out to approximately 1500 and 750 feet fzra shore, respectively.
This indicates the presence of a return flow along the sides of the plume in the near shore region, supplying water of offshore origin for entrainment.
Indeed, such a return flow must occur based on conservation of mass principles.
The plume is entraining local lake water and transporting it out into the lake. This offshore transport of lake water must be replaced by an equal onshore rovement of lake water.
The offshore water will, therefore, be the supply of most of the near shore entraining water.
In the offshore regions where the normal lake flow is sufficient to supply the plume with entraining water, the principle of conservation of mass still dictates a current opposite in direction to the plume.
Such a countercurrent is usually found under the plume when the plume is not contacting the bottcm.
Indeed, proof of such an onshore current has been found at the Ginna site, as will be shown in the biological discussion which follows.
How much of the entraining water in the offshore region is the normial lake flow and how much is the onshore countercurrent is a matter of conjecture.
It should be noted, however, that at offshore locations where the plume is not in contact with the lake bottan, the plume is quite wide and not very deep.
Therefore, it is reasonable to presume that rost of the water being entrained into the plume is coming from the lower edge of the plume.
Since the countercurrent is located beneath the plume, where most of the entrairment is occurring, one can conclude that much of the entraining flow has its origins offshore of the plume area.
5.1-5
5.1.2 BIOLOGICAL ASSESSMENT For the purposes of determining the numbers of macroin vertebrates and ichthyoplankton entrained into the plume the following assumptions were made:
(1)
Only that water which is entrained within the 3°F or greater isotherm could produce a thermal impact on organisms carried along, (2)
Water entrained from the lake flow is the only water assumed to contain organisms, and (3) that component flowing shoreward as part of a limnetic countercurrent is assumed to be organism free.
With these assumptions in mind, the following methodology was used.
Sampling stations along the E-0 transect, running lakeward from the discharge, at 2.5m, 5m, and 8m of water depth correspond to plume centerline distances of 650',
1250' and 2500' respectively.
To determine the numbers of organisms en trained, water volumes and organism concentrations were estimated for each of the plume segments 0 to 6501, 650' to 1250' and 1250' to 2500'.
Concentrations of Gammarus at each station and in the area of the intake were determined from the 1975 Ginna Benthic Report (RG&E, 1977).
Concentrations of Larvae and Eggs were de termined from the 1974 Study presented in RG&E,(1975), Appendix A74.1-3.
From the 1975 Entrainment Report (RG&E, 1977) the average monthly entrainment of Gammarus, Fish Eggs and Fish Larvae as the number per 1000m3 of flow, were calculated for the growing season.
C;.1 -f;
This was compared to the concentration of each organism or group found in the vicinity of the intake to determine the ratio of entrainable organisms in the water column to the concentration found around the intake or on the bottom.
By extrapolating back to shallower depths (2.5m, 5m and 8m) the probable numbers of each organism, or group, which were available for entrainment within each plume segment were determined and expressed as the number per 1000m3 of water.
These numbers are listed on Table 5.1-3.
Information contained in Table 5.1-1 was used to calculate the average amount of lake flow water which would be entrained into the 3°F isotherm during a 30 day month fof each segment of the plume.
Table 5.1-2 lists these flow values.
By mul tiplying the probable concentrations of organisms by the flow values, expected monthly entrainment values for each plume segment, and the total plume were determined.
These numbers are presented in Table 5.1-3, and show that the maximum expected entrainment would be 18,970,659 Gammarus, 12,240,910 Fish Eggs, and 1,715,850 Fish Larvae per month from May through September when the organisms are present in the area.
During the other months, especially the winter months, plume entrainment of these organisms would approach zero.
5.1-7
Studies of the distribution of Asellus, the aquatic sow bug, have shown the presence of a persistent, cold countercurrent flowing shoreward beneath the thermal discharge plume (RG&E, 1977).
Concentration of Asellus are usually found lakeward of the 12m depth out into 35 to 40m of water.
In the 1975 Benthic Report (RG&E, 1977),
it is clearly shown that Asellus were present beneath the plume in concentrations significantly greater than at the comparable stations along the control transects.
This strongly supports the presence of a persistent countercurrent but says nothing of its magnitude.
For the purpose of this dis cussion, it is assumed that this countercurrent is free of any of the representative important species (RIS).
Calculations were made to determine the levels of entrainment expected assuming that 10 percent, 50 percent and 90 percent of the entrained water came from this countercurrent (Table 5.1-4).
Although the exact volume of the countercurrent is not known, it is most likely contained within the range of 10 percent to 90 percent of the total entrainment flow.
This countercurrent, depending upon its magnitude, could reduce the numbers of en trained organisms significantly as is shown in Table 5.1-4.
5.1-8
Certain factors regarding these entrained organisms are im portant.
First, Gammarus entrained into the plume will never experience sufficient thermal stress to produce a lasting biolo gical effect, sc that the actual numbers entrained have no bearing on their survival.
The only effect could be a slight lakeward displacement of their concentrations.
However, when viewing this it must be kept in mind that a natural shift in wind direction can displace tons of water several miles offshore, causing a complete replacement of the shore water.
Temperature recorders placed on nets around the discharge area and along the control transect have shown temperature changes of 10 to 15°F in a few hours.
Second, most of the fish eggs found in the area are assumed to be alewife eggs.
These eggs are dimersal, and adhe sive when alive.
This would indicate that the eggs found within the water column are non-viable.
Support is also lent by our finding that eggs from benthic cages at Ginna were successfully hatched in an aquarium, while eggs collected from the water column in the same area were not.
This would indicated that very few of the eggs entrained into the plume are viable, greatly reducing the possible impact.
Lastly, although the thermal stress information is scant it would appear that only a very small portion of the plume is sufficiently warm enough to thermally stress the fish larvae in the area.
This would result in the actual numbers of larvae impacted by plume entrainment being much lower than the numbers entrained into the plume.
5.1-9
The above discussion serves to demonstrate that the actual impact of the plume entrainment is not necessarily reflected in the numbers of entrained organisms, and that the consideration of other factors is important.
Taking the aforementioned factors into consideration it is concluded that the actual effects of plume entrainment on the area populations of the RIS are negli gible.
5.1-10
TABLE 5.1-1 AMBI=HT AND ERAfWlING WAER FUN RAMES Lake Flow Rate (cfs) 0 80 280 610 1030 1540 2250 3130 4190 5440 6780 Expected Spring 30 F Entrairment Flow (cfs) 0 340 760 1150 1530 1880 2230 2530 2690 2720 2650 Extreme Sping 30 F Entrairm'ent Flow (cfs) 0 160 330 620 810 1000 1180 1350 1520 1690 1840 Distance Off -- re (feet) 0 250 500 750 1000 1250 1500 1750 2000 2250 2500
Table 5.1-2 Projected Plume Entrainment of Ichthyoplankton and Macroinvertebrates Segment of Plume Feet Offshore Water Entrained m3 /month (>3 0F)
% Local Water Entrained Local Water Entrained m3 /month 72,964,800 65,033,280 56,505,600 48 82 100 35,023,104 53,327,289 56,505,600 0
650' 1250' 650' 1250' 2500'
Table 5.1-3 Projected Plume Entrainment of Ichthyoplankton and Macroinvertebrates
/
Organism or
- Entrainable Expected Entrainment Group Segment of Plume Per 1000m3
- /month (May -
Sept.)
Gammarus 0
600' 288.179 10,092,923 600' 1250' 138.059 7,362,312 1250' 2500' 26.819 1,515,424 Total 18,970,659 Fish Eggs 0
600' 138.6 4,854,202 600' 1250' 108.0 5,759,347 1250' 2500' 28.8 1,627,361 Total 12,240,910 Fish Larvae 0
600' 1250' 600' 1250' 2500' 10.49 11.66 12.86 Total 367,392 621,796 726,662 1,715,850
Table 5.1-4 Projected Plume Entrainment Assuming Various Levels of Countercurrent Mixing Organism or Group Maximum Total Monthly Entrainment 10%
50%
90%
Entr inmeUJtJ.
L1u L Countercurrent Gammarus Fish Eggs Fish Larvae 18,970,659 12,240,910 1,715,850 17,073,593 11,016,819 1,544,265 9,485,329 6,120,455 857,925 1,897,066 1,224,091 171,585
1000
- 2000, 3000 ILaNGITUDINAI DISTANCE AIlWG PLMrE
~M~LINE-FE'T FIGUREE 5.1-1 ISOTIRMAL FlOW RATES-ECPECrED SPRIN~G CONDITIONS 14001 1201 I
6001 4001 0
2000 4000 6000 8000 LCNGITUDMIAL DISTANCE ALONG PLUME CEI LNE-FEET FIGURE 5.1-2 ISOTHERMAL FlOW RATES-EXTREME SPRING CCNDITICNS 10000 8000 6000 4000
EFFECTS ON FISH MIGRATION A continual tagging effort from 1973 -
1976 has been carried out at Ginna.
Additional tagging studies have been conducted in the Nine Mile Point area (NMPC, 1977).
From the tag returns for these tagging programs there is enough evidence to determine for some species that the thermal discharge is not a strong attractant.
For other species there is in sufficient evidence to make a good determination but never theless it appears that the thermal discharge does not exert a strong holding power on any species for which there is data.
The species concerned here are those which are large enough for tagging purposes and comprise the major portion of the larger fish excluding the salmonids.
The patterns of fish movement and distance of movement often passed one or more thermal discharges and indicates that there is
- little, if any, interference with shorewise move ment of fish.
Further, it can be demonstrated that whenever there is heavier wave activity, a common occurrence is that fish move offshore and it is unreasonable to suppose that they are capable of returning shoreward to the same location.
Rather the tag return data supports the observation that fish are generally carried eastward by the predominant counterclockwise current in the lake.
In the Ginna area only 20% of all species have been recaptured west of the 5.2-1 5.2
point of tagging.
Other research results by Kelso (1974 and 1976) using the sonic tagging technique indicate almost constant movement back and forth along shore.
To be sure these studies do indicate that a thermal discharge may at tract and hold a fish for a short period of time, but no holding period of greater than 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br /> was recorded.
The following summary of the fish tag returns tagged at the Ginna Nuclear Power Station provides the main suppor tive evidence indicating unrestricted movement.
In these studies more than 3,000 fish were tagged from 1973 through 1976 and from these over 100 fish tag returns were received.
Briefly, the results may be summarized as follows:
- 1) Less than 25% of the fish tag returns were from less than one mile from the point of tagging.
If we assume these tag returns are representative of the residents in the area, then it can be said that 75% of the larger fish in the area are moving away and are not held in the area.
- 2)
Looking at the tag return data more closely, only ten tag returns in the area less than one mile were from fish recaptured more than ten days after tagging.
If we assume (conservatively) that these represent t-he resident popula tion in the area, then only 10% of the fish tagged would represent the resident population in the area (of the larger fish).
This is based on the assumption that those 5.2-2
fish recaptured in the area less than ten days after tagging will move away.
- 3)
The fish tag returns strongly support the hypothesis that between 75 and 90% of the larger fish are not held by the thermal discharge.
One can look at these returns in another way.
It can be assumed that 75 to 90% of the larger fish were, in fact, being tagged as they moved past the Ginna discharge.
Experience has indicated that, in fact, a percentage of almost every species of larger fish may remain in one area for long periods of time and since there is movement back and forth along the shore, some fish being recaptured at the Ginna site may, in fact, have returned to the area after a lengthy period of time in some other part of the lake.
Certainly this has been demonstrated for yellow perch in other fish tag studies (NIPC, 1977).
Looking at the Ginna fish tag data alone, however, it can be seen that at least 8 of the tag returns were from the area east of Nine Mile Point.
Fish tagged at Ginna had moved along the shore eastward past the thermal discharges at Oswego, Nine Mile fl, and possibly Fitzpatrick.
There is little reason to assume, therefore, that any type of thermal discharge is preventing fish from moving freely along the shore.
5.2-3
5.3 Potential for Gas Bubble Disease 5.3.1 General Description Gas bubble disease (GBD) is a collective condition exhibited by fish when exposed for some critical duration to water supersaturated with some critical threshold of dissolved gas.
Obvious external symptoms of GBD, reflecting the lodging of gas bubbles in tissue, include emphysema of the fins, cutaneous blisters on the head and in the mouth, emboli in the lateral line, and exophthalmia (bulging eye condition).
In addition there are often other less obvious but more fatal internal symptoms of GBD such as accumulations of gas emboli in the heart, ventral aorta, and gills, any of which could lead to anoxia and death (Stroud and Nebeker, 1976).
Susceptibility and sensitivity to GBD appears to vary among species and among different sizes within a single species (Dawley et. al.,
1976; Bouck et. al., 1976, Nebeker and Brett, 1976, and Rucker, 1976);
salmonids in general exhibit a greater sensitivity, and larger fish (coho 8 to 10 cm) appear less resistant than smaller specimens (3.8-6 cm).
Although GBD may not be fatal, it may render fish more susceptible to secondary infections, predation, and less responsive to other environmental stimuli.
Depending upon the extent of sublethal symptoms, GBD may be reversed if fish are provided waters with sufficient depth and/or total gas levels at or below saturation; since gas solubility in body tissues increases 5.3-1
with water depth, bubbles may be resorbed.
Likewise in waters with gas at, or below, saturation levels, the fish can exhaust excess gases dissolved in their tissues, resulting in bubble resorption.
Exophthalmia may be reversed, however the eye lens is often permanently displaced rendering the fish blind.
5.3.2 Cause Nitrogen is suspected of being the prime cause of GBD because it is the least soluble of the three principal gases in water (oxygen, nitrogen, and carbon dioxide),
and is not removed from the dissolved state by chemical combination with blood components (Adair and Hains,1974).
When fish acclimated to ambient gas saturation levels enter super-saturated waters,there is a net flow of gas across the gill membrane and into the fishes blood.
If the fish is unable to metabolize the newly acquired gas (which is especially true for nitrogen) it tends to come out of solution, giving rise to the various bubble-associated, internal and eventually external symptoms.
The warming of fish may aggravate internal problems since the solubility of gas is inversely related to temperature.
5.3.3 Threshold Studies While nitrogen is usually implicated in GBD, recent studies have shown two variables to be particularly crucial in the development of GBD; they are oxygen-nitrogen saturation ratios, and total gas (TG) pressure or saturation (Nebeker et. al., 1976; Rucker, 1976, 5.3-2
and Nebeker and Brett. 1976).
Experiments with three species of salmonid smolts, at a temperature of 12 0 C (53.6°F),
revealed a lethal threshold of 114.5 percent saturation of total gas (TG) for coho, 113.5 percent for sockeye, and 114 percent for steelhead trout.
Ninety-six hour LC50 values were 120.5, 116.7, and 116.0 percent (TG) for coho, sockeye, and steelhead respectively.
Non-lethal external symptoms were apparent at a TG level of 110 percent.
For any given TG saturation level, Nebeker et. al. (1976) found a significant decrease in mortality of juvenile sockeye when the ratio of oxygen to nitrogen was increased; however they found much more extensive and severe external signs of GBD at high 02/N ratios than at low 0 2/N 2 ratios, suggesting that oxygen plays a significant part in forming external emphysema and lesions.
As an example of ratio effects, 50 percent of the test specimens died after 71 hours8.217593e-4 days <br />0.0197 hours <br />1.173942e-4 weeks <br />2.70155e-5 months <br /> at 120 percent TG when 0 2 /N 2 ratio was 117.2/
121.3 percent; however only 7 percent died after 167 hours0.00193 days <br />0.0464 hours <br />2.761243e-4 weeks <br />6.35435e-5 months <br /> when the 02 /N 2 ratio was changed to 170.5/107.0 percent.
Coho salmon fingerlings respond similarly at a temperature of 13.6 0 C (56.50F) and constant TG of 119%; when maintained at an 0 2/N2 ratio of 173/105 percent, 25 percent of the fish died after 34 days, whereas at a ratio of 75/131, 25 percent died in only 2.3 days (Rucker).
The important point of these studies is that supersaturation of waters solely with oxygen, will not be sufficient to produce fatal 5.3-3 I
GBD; a critical level of nitrogen saturation (109 percent in the case of coho),
and a critical level of total gas (TG) saturation, must be achieved.
5.3.4 Case Histories of GBD at Thermal Discharges Dissolved gas supersaturation in the thermal effluent of a power plant occurs because of the inverse relationship between gas solu bility and temperature in water.
When intake waters are at or near saturation with oxygen and nitrogen, and subjected to substantial temperature increases as a result of condenser passage,particularly in winter, the discharged waters will become supersaturated with gases.
The decrease in ambient pressure between intake and dis charge also contributes to supersaturation.
From a purely theoretical standpoint, fish subjected to supersaturated thermal discharge waters for a critical period should contact GBD and succumb.
However for various reasons, such as plume avoidance in winter by most fish, short residence time of those that do en counter a plume, sub-critical threshold levels of supersaturation, or some unknown physiological condition, there have been very few reported incidents of fish kills attributed to GBD at power plant discharges (Marcello and Fairbanks, 1976).
There are two often cited, but insufficiently.described, cases of fish kills associated with GBD which warrant discussion.
The first and most cited case occurred in the heated effluent from Marshall Steam Station, located on Lake Norman, N.C.,
during the 5.3-4
winter months (especially February and March) of 1971 (Miller, 1974; Adair and Hains, 1974).
The incidence of GBD was particularly high in 1971 relative to the previous or following winter at that station.
A careful examination of the data results in the following important points:
- 1) At values and discharge flows were extremely high in 1971; At's were in the range of 13.6 to 15.9 0 C (24.6-28.6°F) with intake temperatures of 10.6 5.4 0 C (51.1-41.8°F) from January to March in 1971.
This contrasts with At's of 10.8-11.5 0 C (19.5 20.70F) during the same period in 1972, and 11.6 15.7 0 C (20.9-28.3°F) in 1970.
- 2)
Average 02 /N 2 saturation ratios of discharge water were 118.7/132.4 percent (maximum critical 111.2/
144.2) in the winter of 1971, versus a lower average 119.2/121.3 (maximum critical 124.9/130.6) in 1972.
- 3)
The most sensitive species were white bass (Morone chrysops) and crappies (Pomoxis spp,), with crappies comprising the bulk of the fish kill.
- 4)
Concurrent sampling at other thermal discharges in the general vicinity in 1972, revealed practically no fish (3 out of 1305 captured, and 1 out of 586) 5.3-5
with symptoms of GBD.
These other two stations had At's ranging from 6.3-12.0 0 C (11.2-21.6°F) in winter, and N2 saturation values exceeding 110% during only January.
- 5)
Adair and Hains (1974) conclude that the primary cause of GBD and a fish kill at the Marshall Station in 1971 was the high At giving rise to N2 saturations above 110% over a long period of time.
A second noted case of fish kills and GBD, centers about the sub stantial mortality of Atlantic menhaden in the discharge canal and plume of Boston Edison Company's Pilgrim Nuclear Power Station (Cape Cod Bay) during April 8-24, 1973 (Marcello and Fairbanks, 1976).
The salient features of this case are:
- 1) discharge temperatures ranged from 13.9-22.8°C (57-73 0 F),
and At's ranged from 7.2-12.2 0 C (13 22 F),
- 2) 02 saturation values ranged from 123-142%, unfortunately the most important and likely critical parameters (N2 saturation and total gas saturation) were not
- reported,
- 3) the primary species killed is a marine fish, Atlantic menhaden; studies are being conducted to establish 5.3-6
its tolerance to supersaturated waters, and elucidate possible modifying factors such as physiological stress.
- 4) a large school of menhaden encountered the same discharge for 1-day in July 1973 when temperatures ranged from 20-27.80C (68-82°F) and 02 saturation ranged between 124 and 146 percent.
None of the several specimens examined in that study showed external signs of GBD and no deaths were observed in the area.
5.3. 5 Potential for GBD at Ginna Given the above discussion and conditions accompanying actual fish kills due to GBD in other thermal discharges, attention is now directed toward the potential for impacts due to GBD at thermal discharges in the Great Lakes, and in particular at Ginna.
A recent study was reported by Otto (1976) on work conducted at the Waukegan and Zion generating stations on Lake Michigan.
Their objective was threefold:
(1) determine 02 and N2 saturation levels in intake and discharge waters; (2) sample fish in the thermal dis charge areas and observe for signs of GBD; and (3) determine experi mentally, critical gas saturation levels for yellow perch and rainbow trout.
The Waukegan is a fossil-fuel facility with a shoreline intake and discharge system (maximum At of 90 C (16.2°F));
5.3-7
Zion Nuclear Station has an offshore submerged intake (7M),
and an offshore diffuser discharge (maximum At of 11 C (19.8 0 F).
The following summarizes Otto's findings:
- 1) during mid-winter when lake waters are coldest (0 C) and saturated with gases, supersaturation levels in the Waukegan and Zion discharge waters may be as high as 125 percent and 132 percent, respectively;
- 2) examination of fish captured in the vicinity of the Waukegan discharge, which included rainbow, brown, and brook trout species, plus coho salmon, northern pike, spottail shiners, carp, and white suckers, showed that all with the exception of carp did not have symptoms of GBD; this is interesting because shiners, carp and suckers inhabit the intake and discharge canals throughout the year.
Otto attributes the absence of symptoms to fish having short residence times in the area of potential impact.
- 3) yellow perch tested in an experimental facility, using heat to produce supersaturation, were un affected by gas saturation levels as high as 115 percent, and have an 8-day median lethal saturation level of 126 percent; rainbow trout were unaffected by saturation levels of 110 percent, and have an 5.3-8
estimated 8-day median lethal level of 119 percent.
Focusing on the potential for GBD at Ginna, the applicant has conducted fish studies in the winter (both gill netting and with TV monitoring in the discharge canal)
(RG&E, 1976 a, 1976 b) to assess the types present and their relative abundance.
The major species found in discharge waters during February 25, 1975 were lake chub, gizzard shad, and white perch; a few spottail shiners, one smelt, and one brown trout were also taken.
TV monitoring during daylight in January and February revealed mainly gizzard shad, with an occasional cyprinid and white bass.
It is obvious that the major winter fish at Ginna do not include those species associated with GBD kills at thermal discharges discussed above.
This feature, in conjunction with a general low abundance of fish, and especially few sensitive salmonids, would tend to mini mize the potential for GBD impact at Ginna.
None of fish sampled or observed during these two winter months at Ginna had signs of GBD.
It is reasonable to assume, in the absence of actual measurements at that time, that discharge waters (temperature of 15.6-16.1 0 C) were supersaturated with oxygen and nitrogen as a result of decreased pressure (withdrawn from about 8m (26 feet)) and elevated temperatures (about 11-120 C).
Yet the findings of no fish with external signs of GBD corroborate those reported by Otto (1976) for the Waukegan and Zion Stations on Lake Michigan.
The applicant contends, based on supportive evidence, that relatively few fish occupy the discharge waters during critical 5.3-9
winter months, and those few fish encountering the plume region do not occupy the discharge waters for a sufficient period of time to experience GBD.
5.3-10
LIST OF REFERENCES Adair, W. D.,
and J.
J.
Hains. 1974.
Saturation values of dis solved gases associated with the occurrence of gas-bubble disease in fish in a heated effluent.
In:
Thermal Ecology, J.
W. Gibbons and R.
R. Sharitz (Eds.),
AEC Symposium Series (CONF-730505),
Augusta, Ga.,
pp. 59-78.
- Bouck, G. R.,
G. A. Chapman, P. W. Schneider, Jr., and D. G.
Stevens.
1976.
Observations on gas bubble disease among wild adult Columbia River fishes.
Trans. Am. Fish. Soc. 105: 114-115.
- Dawley, E.
M.,
M. Schiewe, and B.
Monk.
1976.
Effects of long-term exposure to supersaturation of dissolved atmospheric gases on juvenile chinook salmon and steelhead trout in deep and shallow test tanks.
In:
Gas Bubble Disease.
Proceedings of a Workshop held at Richland, Washington, AEC & Battele, CONF-741033, pp. 1-10.
Kelso, J.R.M.,
1974.
Influence of a thermal effluent on movement of brown bullhead (Ictalurus nebulosus) as determined by ultra sonic tracking.
J. Fish. Res.
Bd. Can. 31:
1507-1513.
- 1976, Movement of yellow perch (Perca flavenscens) and white sucker (Catostomus commersoni) in a nearshore Great Lakes habitat subject to a thermal discharge.
J.
Fish. Res.
Bd. Can. 33:
42-53.
5.3-11
N LIST OF REFERENCES (Cont'd)
Marcello, Jr.,
R.
A.,
and R.
B. Fairbanks. 1976.
Gas bubble disease mortality of atlantic menhaden, Brevoortia tyrannus, at a coastal nuclear Power plant.
In:
Gas Bubble Disease.
Proceedings of a Workshop held at Richland, Washington, AEC & Battele, CONF-741033, pp. 75-80.
Miller, R. W. 1974.
Incidence and cause of gas-bubble disease in a heated effluent.
In:
Thermal Ecology, J.
W. Gibbons and R.
R.
Sharitz (Eds.),
AEC Symposium Series (CONF-730505),
Augusta, Ga.,
pp. 79-93.
Nebeker, A.
V.,
G. R. Bouck, and D. G. Stevens. 1976.
Carbon dioxide and oxygen-nitrogen ratios as factors affecting salmon survival in air-supersaturated water.
Trans. Am. Fish. Soc.
(3):
425-429.
Nebeker, A.
V. and J.
R. Brett. 1976.
Effects of air-supersaturated water on survival of pacific salmon and steelhead smolts.
Trans.
Am. Fish. Soc.
(2):
338-342.
Niagara-Mohawk Power Corp.,
1977.
Lake Ontario Fish Tag Report Summary 1972-1975.
Prepared by J.
F. Storr Ph.D.
5.3-12