ML20079N109
| ML20079N109 | |
| Person / Time | |
|---|---|
| Site: | Quad Cities  |
| Issue date: | 03/16/1981 |
| From: | COMMONWEALTH EDISON CO. |
| To: | |
| References | |
| RTR-NUREG-1437 AR, NUDOCS 9111110083 | |
| Download: ML20079N109 (214) | |
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Supplement to 316(a) and 316(b) Demonstration for ThE QUAD CITIES NUCLEAR GENERATING STATION k
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Commonwealth Edison Company Chicago, Illinois March 16, 1981 9111110083 810316 PDR- NUREO 1437 C PDR
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O Table of Contents l l
Section Title a P_nge, Acknowledgments 11 Introduction 1
'I Executive Summary 6
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l I Description and History of Station l Operation 14 II 316(a) Demonstration Supplement 28 l l
A. Hydrological 6 -d Thermal Investigations 28
- 1. Critical Flow and Water Temperature Conditions for >
the Mississippi River at
__ ,p. Quad Cities Nuclear Station 28
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- 2. Thermal and Hydrologic Per-formance of the Quad Cities -
Nuclear. Station Waste Heat Diffuser System Id
-B. Summary of-Biological Monitoring Studies 96 C. Effects of Increased Temperatures on Fish 117
, III 316(b) Demonstration Supplement 144 A. Entrainment Studius 145 -
B. . Impingement Studns 155 I:
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Acknowledgetents This report was reviewed by a number of Commonwealth Edison Company consultants including Dr. Roy C. Heidinger, Southern Illinois University, Dr.
i k'1111am I.evis, Snuthern 1111nois University. Dr. S. C. Jain, University of Iowa, Dr. J. F. Kennedy, University of Iowa, Dr. P. K. Kitanidis, University of Iowa, Dr. Donal.d B. Mcdonald, University of Iowa and Dr. Robert C. Otto, R. G. Otto and Associates. Their constructive criticism and recommendations were greatly appreciated and contributed significantly to this report.
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Introduction O This summary reviews operational monitoring and special studies con-ducted at Quad Cities Station. Cased on the results of these programs, Common-wealth Edison Company believes that it has been adequately demonstrated that no ady tae impact on the fish and shellfish populations results from operation of the present intake or discharge during open-cycle cooling, and that there now exist sufficient data to justify relief from the closed-cycle cooling re-i quirements for both units.
This summary is a supplement to the document previously submitted to Region V, U.S. Environmental Protection Agency (USEPA) by Commonwealth Edison
- Company (Commonwealth Edison company,1975) in support of its application for an alterne.te effluenc-limitation at Quad Cities Station under Section 316(a) of <
-the Federal Water Pollution Control Act (TWPCA). This report also serves to up-l l date Commonwealth Edison's demonstration under Section 316(b) of the FWPCA i
l' that no significant adverse environmental impact will result from operation of 1
j the Station's intake structure during open-cycle cooling.
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- i. The original Demonstrations were submitted to USEPA in two parts. The i
first part of the 316(a) Demonstration ves submitted on February 28. 1975. The 2 -second submittal, which included the 316(b) Demonstration and a suppicment to ,
the 316(a)LDemonstration followed on' April 11, 1975. The 316(a) Demonstration
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- requested-an alternate eff.',uent limitation which would allow discharge to the
- j. Mississippi River equivalent to that of one of the two Quad Cities Station units. i p
The 316(b) Demonstration concluded that no significant adverse environmental im-l , I
-pact results from-the Station's intake during open-cycle cooling water operation. ;
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These updated Demonstrations, however, are for the case where both units are op-
{ erating open-cycle. ,
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1 A preliminary determination was issued by the USLPA on April 4,1977, h vhich indicated that data and analysea presented were insufficient to justify relief from the therral discharge restrictions specified in the fiPDES permit. )
Subsequent information was submitted to L3EFA at its request on :tay 30 June 20 l 1
and July 22, 1977.
Since its start-up in April, 1972, Quad Citics Station has utilized several means of discharging cooling water to the Mississippi River. The origi-nal design proposed that the Station operate open-cycle discharging cooling vater by means of a channel which would convey the water along a straight wing dam into the deeper, higher velocity region of the river. However, a thermal-hyiraulic study (Jain, et al., 1971) predicted that this method of open-cycle discharge would result in a heated plume that exceeded the State of Illinois thermal criteria.
O Model studies conducted by the Iowa lustitute of Hydraulic Research to determine the best method for obtaining rapid mixing of heated and ambient river waters narrowed the alternatives to some type of multiport diffuser sys-tem (Jain, et al., 1971). Since sufficient time was not availabic to adequately design, test and install the multiport diffuser system prict to Station start-up, an interim side-jet system was developed. This system operated from the time of Station start-up (January,1972) until August, 1972, when the diffuser system was placed into operation.
Commenvealth Edisen Company entered into an agreement with the Attor-ney General of the State of Illinois, Izaak Walton League of America and lilinois State Community Action Program of the United Automobile, Aerospace and O
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O Agricultural Implemer t. Workers on March 27, 1972, requiring that, except in cer-tain circumstances, both units at Qusd Cities ctation be operated with closed-i cycle cooling beginning May 1, 1975. Design and construction of a spray canal S M cGuimately 16,000 feet in length vas, therefore, initiated in 1972 and corpl *ed in 1975. The diffuser system was operated as an open-cycle dis-cha..,e for both unita until May 1, 1974, and subsequently for onc unit until May 1, 1975.
Tests of the closed cycle cooling system, or spray canal, have shown that it operates at substantially less than anticipated efficiency (Freeman, et al., 1980). Since the Station was designed to operate most efficiently at a certain maximum inlet temperature (60'F), when actual inlet temperatures increase above this level not as much power can be generated. As a result, the Station's generating capability is reduced on days when outside temperatures are high and the spray canal is unable to achieve the required minimum level of cooling. .
The auxiliary power required to operate the spray canal is 24 !Ne.
This assumes that all spray modules and the maximum number of lift pumps are operating. Based on Station operating data for an 87 day period during the months of July, August and September, 1978, it was estimated that an average thermal derating of 128 FNe was experienced during partial open-cycle operation. .
On July 9, 1979 Commonwealth Edison Company received a revised NPDES permit for the Station. The pemit, effective August 2, 1979, and to expire on September 30, 1980, was jointly issued by the Illinois Environmcatal Protection Agency and the Iowa Department of Environmental Quality. It' allows partial O
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open-cycle operation of the condenser cooling system at times when the tempera-ture of the water returning from the spray canal exceeds 93'T ot during certain infrequent maintennce periods when the Station water exceeds 85'T. This was f ollowed in August, 1979, by an interim modification by the parties to the closed-cycle operation agreements of March 1972, which allows partial open-cycle operation of the Station when required to avoid su'ostantial capacity losses.
This interi.m agreement will continue until parties to the original agreement make a final determination with respect to the cooling water system to be used at the Station.
Numerous hydrological and biological studies and data reviews have been conducted since submittal of the original 316(a) and 316(b) Demonstrations.
The studies have included special investigations to document effects of open-cycle operation during the low flow year of 1976. The reviews include g consideration of the hydrological data base and the results of monitoring studies conducted from 1968 through the present. Also included is a review of the physiological effects that elevated temperatures might have on the fishes of Pool 14. This subject, which has never buen addressed before the Quad Cities Station discharge is discussed in a separate section of this report as part of the supplement to the 316(a) Demonstration. On the basis of thie new information and on the expanded consideration of the results of the monitoring program, Commonwealth Edison Company requests that Quad Cities Station be permitted to operate open-cycle using the diffuser system an. a means of disch,arge.
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Literature Cited l
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Commonwealth Edison Company, 197$. Three-Sixteen a 6 b Demonstrations. Quad Cities Nuclear Station Mississippi River. A demonstration to the United. ;
States Environmental Protection Agency. 264 pp. I 1
Jain, S.C., W.W. Sayre Y.A. Akyeampong, D. McDougall and J.P. Kennedy, 1971. !
Model Studies and Design of Thermal Outfall Structures Quad Cities Nuclear Plant. Iowa Institute of Hydraulic Research, The University of lova, !
Iowa City, Iowa. 11HR Report No.135. 101 pp. i Freeman, Jesse and James Skridulis, 1980. Implementation of the QCNPS Canal / Lift l Pump System Code at the Quad Cities Nuclear Power Station: Program
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Development and Operational Experience. NUS Corporation NUS-3425. Rockville, ;
Maryland. l i
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Executive Summary Quad Cities Station is a nuclear-fueled steam electric generating faci-lity located on the Illinois shore of Pool 14 of the FMssissippi River at River Mile 506.$. The Station utilizes two boiling water nuclear reactors, each unit producing 609 megavatts electric (MWe) power for a total Station output of 1618 MWe. Make-up cooling water for Quad Cities Station is withdrawn from the His-sissippi River, circulated through the Station and directed through a spray canal system from which it is recirculated to the Station. This cethod of operation is called closed-cycle. The Station may also be operated open-cycle where cooling water after circulation through the plant's condensers is dis-charged to the Mississippi River through a two pipe multiport diffuaer system in the riser. Finally, the Station may be operated in a partial open-cycle mode. In this operating mode approximately 50% of the cooling water discharge is circulated through the spray canal system while the remainder is discharged through one or both of the diffuser pipes.
From January, 1972 until May, 1974, when the sptay canal system began operation, Quad Cities Station operated in the open-cycle mode discharging con-denser cooling water to the river via a side jet canal from January through July, 1972 and via the diffuser system from August, 1972 through April, 1974.
In accordance with an agreement between Commonwealth Edison Company and the Attorney General of the State of Illinois, the Izaak Walton League of America and the United Automobile Workers of America, which requires closed-cycle cooling, operation of the spray canal commenced on May 1,1974, with the Station operating with the equivalent of one unit discharging cooling water to the canal and one unit discharging directly into the river. This mode of operation con-tinued until !by 1,1975, when cooling water f rom both units vss routed to the canal (closed-cycle).
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l closed-cycle operation continued until August 2, 1979, upon receipt of the currently applicable NPDES permit for the Station which allows partial open-cycle operation of the condenser cooling system at times when the tem-peratura of the water returning from the spray canal exceeds 93'F. Operation of the Station is also tiubject to an interim modification effective August 27, 1979, by the parties to the closed-cycle agreement which allows partial open-cycle operation of the Station when required to avoid substantial capacity i i
losses.
This document in a eupplement which updates the document previously !
submitted to Region V, U.S. Environmental Protection Agency by Commonwealth Edison Company in 1975, and subsequent updates in 1977, in support of its application for an alternate effluent limitation at Quad Cities Station under
$ action 316(a) of the Federal Water Pollution Control Act (IVPCA). This
. summary also serves to update Commonwealth Edison Company's Demonstration, submitted in 1975, unoer Section 316(b) of the FWPCA that no significant adverso environmental impact will result from operation of the Station's intake during open-cycle-cooling water operation. The 516(a) Demonstration requested an-alternate effluent limitation which would allow diccharge to the 111ssissippi
. River equivalent to that of one of the two Quad Cities Station units.
This document reviews numerous hydrological and biological studies -
and data reviews ttat have been conducted since submittal of the original 316(a) and 316(b)-Demonstrations. These revicvs include consideration bf the hydro-Jogical_datt. base, results of biological monitoring studies conducted from.
1968 through the present, as well as a review of the physiological effects that elevated temperatures might have on the fishes of Pool 14. Ou the basis O
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1 of this inf ormation, Commonwealth Edison Company requests that Quad Cities Station be permitted to operate open-cycle using the dif fuser system as a means of discharge.
The diffuser pipe system for Quad Cities Station has been investigated 4
through analysis of laboratory test data and field data collected for a wide range of river discharges with the plant operating at full load and at various partial loads. With the plant operating at full load in the open-cycle mode, tests indicate that temperatures at the edge of the mixing zone meet applicable state standards for all river flows greater than approximately 16,000 cis.
Mississippi River flows at the location of Quad Cities Station exceed 16,000 cf a about 98% of the time.
Environmental studies including many intensive monitoring and special programs began in 1965 with several of these programs still continuing. Water quality as well as the nature and abundance of the biota in Pool 14 has been evaluated during those programs.
Water quality in the river was measured from 1968 through 1977. Re-a sults showed water quality in Pool 14 to generally be good. Although there have been periods of degraded water quality which resulted in occasionally high 4
levels of total tron, mercury, manganese, copper, hexane soluble materials and phenols, increased concentration of these materials were in no way attributable to Station operation.
Studies of the lower trophic level biota (phytoplankton, zooplankton, periphyton and benthos) were conducted from 1968 through 1977. Results of these i O
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i studies have shown that Station operation has not adversely affected population ;
levels in these various groups. No consistent changes in species composition or distribution of those organisms were observed between control and potentially !
impacted sampling locations in the tiver associated with diffuser operation. l These programs were sensitive enough to have detected short or long term !
effects that Station operation might have had on the water quality or aquatic .
biota of the pool. This f act was continually demonstrated in that natural t variation between seasons, years and major habitat types could be defined with confidence in addition to the detection of numerous localized effects as- ;
sociated with Station operation. These effects wnre expected and their detection demonstrates that the monitoring programs were sufficiently sensitive ,
to have detected any major perturbations had they occurred.
ichthyoplankton studies have been conducted from 1971 through the present with comparisons for this Demonstration made from 1975 throug,h 1979. i Taxa of eggs and larvae collected over this period of time have remained con-stant with freshwater drum, carp!and cyprinids (minnows other than carp) being i
, the most abundant taxa. Ambient river water temperatures-appear to directly l influence the density of ichthyoplankton. However, in general there has not been any obvious correlation with river flow. An intensive sampling program
-conducted in 1978 showed there was-little difference betweep average day and night abundances of total larvae. Although there was little difference in the vertical distribution of these organisms, horizontal differences were noted with the main channel and 1111nois side of the river exhibiting somewhat higner total' larvae abundance. During 1978 and 1979, sampling conducted also showed fresh-water drum eggs and larvae were abundant at all locations upstrean of the O
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Station and demonstrated that all of Pool 14 in this area is a spawning and h nursery area for this species.
Adult and juvenile fish monitoring has been conducted in the area of ,
Quad Cities Station since 1971. Methods of sampling have included electro-shocking, bottom trswling (1971-1979), haul seining (1978 and 1979) and sampling of selected slough habitats using a cove rotenone techniqac (1977 and 1979).
Results of these programs conducted each year have shown little signi-ficant variation ir the number of species collected each year. Total catch-per-effort values (without gizzard shad) from the electroshocking progtam, re-mained similar among the one year of preoperational monitoring (1971) and the t
first two years of operatidnal monitoring (1972 and 1973) when the Station oper-ated open-cycle. There was, however, a fairly steady pattern of decline through- llh out the study area f rom 1974 through 1919, when the Station principally operated closed-cycle or partial open-cycle. Since the deercase was observed at both up-stream (control) and downstream (potentially impacted) locations, it cannot be _
attributed to thermal discharge associated with Station operation.
It can be hypothesized that the catch-per effort was higher during the earlier open-cycle years than during the later closed-cycle years because Station operation affected subsequent population levels due to entrainment and impinge-ment. This hypothesis was discarded, however, because entrainment loshes were shown to be about the same for open and partial closed-cycle operation. Impinge-ment losses have also been shown to be very low (less than 1% of the standing stock in Pool 14). Thus, neither of these factors can be reasonably expected to have resulted in the population decreases seen over the study period.
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O Results of bottom trawling studies have shown very little annual change in species composition of fish in the main channel over the nine year period.
These data, in conjunction with temperature tu evaluate avoidance or attraction i l
of fish to the vicinity of the diffuser system, have also shown there has been no correlation between temperature and fish catches in the area of the diffuser discharge.
The possible physiological effects of Quad Cities Station open-cycle cooling discharge through the diffuser system on fish in Pool 14 of the Missie-sippi River were also evaluated. Effects considered were (a) jet entrainment of planktonic eggs and larvae, (b) plume attraction of juvenile and adult forms, (c) occasional long term exposures (weeks) to low-level temperature increments of
<.3 95'F and (d) the potential for cold-shock and gas bubble disease. Data on fish occurrence and distribution in Pool 14. special m. dies conducted at the ,
Statinn relating to thermal effects as well au sources from scientific litera-ture were evaluated. In addition, procedures recommended by the USEPA for eval-uating thermal effects were employed. These considerations have revealed no ex-1 sting or potential impacts on fish that would be associated with the thermal plume. In fact, temperatures downstream of the Station (82*F after full mixing of condenser discharge with river water) to which even the most sensitive species would be exposed will not exceed maximum weekly average temperature for that species'for extreme conditions of low flow (7Q10) and 100% operating capacity of the Station. Finally, this average maximum temperature is well below the upper incipient lethal temperature for even the most sensitive species in Fool 14.
Since submission of the original 316(b) Demonstration, several studies
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have been conducted to document the effects of open-cycle operation on organisms I
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entrained in condenser cooling vater as well as studies to minimize 1 epic;;ceent and to quantify impingement losses relative to population levels in Pool 14.
Results of entrainment studies for plankton (phytoplankton and :oo-plankton) indicated that the portion ot the plankton assemblage passing the Station affected by Station operation was very lov. The reductions, however, were also sufficiently small that they ve.re not detectable in field prograce in ,
spite of the fact that sampling procedures in those programs were sensitive enough to detect natural variations in this community. It is also evident that entrainmeat effect. on the total plankton community is of no consequente since entra.inment never results in 100% mortality and very smill percentages of 1.he total river flow are used for condenser cooling during open-cyc12 operation.
Elfccts of entrainment from open-cycle operation on ichthyoplankton is also minimal. Special studies conducted to measure the survival of fish larvaa O
paesing through Quad Cities Station condenserr, concluded that entrairrent losses are primarily a function of Station discharge temperatures. Most larvae survive entrainment when discharge temperatures are belov 91.4'F. Further, evaluations of river and Station operating data 1ndicated that most ichthyoplankton pass the Station prior to discharge temperatures reaching these levels. In addition, it was also concluded that there were little meaningful difCerences between esti-mates of total ichthyoplankton abundance lost dua to open-cycle operation and the present operating mode (partial open-cycle operation) where the volume of river water used for make-up is increased when return water from the spray canal ex-ceeds 93*F.
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i O Impingement exploitation rates were estinated and it was concluded based er these projections that losses due to impingement at Quad Cities Station are minimal. Further it has also been demonstrated that placement of a barrier net in front of the forebay has been effective in minimizing fish losses during closed-cycle operation. From these results it is evident that the net would be ef f ective in reducing imoingement during open-cycle operation through the judicious operation of the circulating water pumps and the ice melt line throughout the year.
During the summer months it is expected that impingement can be mini-m1 zed by diverting condenser cooling water back to the forebay through the ice melt line located on the floor of the forebay. This will increase temperatures in the forebay and it is believed that fish will avoid the intake during this
() period of the year.
During the winter months, impingement can be minimized during open-cycle operation by installing a barrier not in f ront of the f orebay in conjunc-tion with reducing the number of operating circulating water pumps and by di-verting condenser discharge back to the intake forebay by means ot the ice melt line. By tedacing the number of operating circulating water pumps in addition to diverting condenser discharge back to the f orebay, intake velocities at the river's edge during open-cycle eperation would correspondingly be reduced, by about 50%, to about 0.5 ft/sec.
A testing period will be needed to define the extent that the barrier net and increased temperatures in the f orebay decrease impingement. The extent of the reduction cannot be quantified without operational data. Existing data
() do demonstrate, however, that. these methods will reduce impingenent.
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Section I ,
Description and llistory of Station Operation O
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j List of Tables if f j Description and History of ;
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List of Figures Figure No. T_itle Page, 1 Geographical Location of Quad Ci+.ies Station 15 2 Quad Cities Station Cooling System Configuration, April, 1972 through July, 1972 16 3 Qttad Cities Station Cooling systco lorfiguration, August, 1972 through April,1974 17 I. Quad Cities Station Cooling System Configuration, May, 1974 through December, 1979 18 5 Flow of Cooling Water through the Quad Cities Station 20 0
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List of Tables Table No. Title _ n P,ay,e, 1 Month):t Capacity Factors. .
Quad Cities Station, August, 1972 through December, 1979 21 ,
l 2 Monthly, Minimum. Maximum and Mean k'ater Temperatures ,
at the Quad Cities Station. ;
August, 1972 through December.
1979 24 -t i
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Description end History of Stetion Operation Quad Cities Station is a nuclear-fueled steam electric generating facility located on the Illinois shore of pool 14 of the tussissippi River ap-proximately 21 miles north of Davenport, Iowa, Moline, Rock Island and East Moline, Illinois (Figure 1). Quad Cities Station utilizes two boiling water nuclear reactors. Each unit produces 809 megawatts electric (Mk'e) power for a total Station output of 1618 !Nc. k' hen operating at maximum capacity in the open-cyc1c mode, cooling water is withdrawn from the Mississippi River at a rate of 2230 cfs. The temperarare of the cooling water is raised a maximum of 23*F before it is returned to tle river, resulting in a heat rejection rate of 11.48 x 109 Btu /hr.
The Station began operation in Jarnary,1972, when low power testing was initiated. Following the completion of low power testing in early April, 1972, sr. art-up testing began and was continued until August, 1972. From January until August, 1972, cooling water was withdrawn f rom the tiississippi River, cir-culated through the condenser cooling systett and discharged through a side-jet discharge canal as shown in Figure 2.
A diffuser system was installed in the Mississippi River in 1972. The diffuser system consists of two 16-foot diameter multi-port manifolds buried in the river bed as shown in Figure 3. Open-cycle, two-pipe diffuser operation be-gan in August, 1972, at which time the use of the side-jet discharge was per-manently discontinued. The diffuser mode of operation continued until 1 May 1974.
On May 1,1974, a new cooling system coraenced operation consisting of a spray canal approxicately 16,000 feet long, 185 feet vide and 9 feet deep (Figure 4). The station operated with the equiva3cnt of one unit discharging cooling water to the canal and one unit discharging directly into the river 14
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- O until May 1,1975, when cooling water f rom both units was routed to the canal. l During closed cycle cooling, thermal effluent is moved from the discharge bay to the spray canal via five lift pumps, each with a capacity of 372 cfs. In the spray canal, 328 spray modules are used to cool the water by evaporative action.
The cooled water is returned to the intake bay by way of a spillway and recircu- ,
lated through the Station condensers. At maximum operating capacity, approxi-mately 2063 cis of water is circulated through the spray canal. Discharge (blowdown) (Figure 4) through a four foot diameter multi-port manifold to the ,
Mississippi River consists of approximately 111 cfs (annual average) of cooling .
water. In addition to the 111 efs blowdown, approximately 56 cfs of water in the spray canal is lost due to evaporation. To make up for these losses, 167 1
cfs of cooling water is withdrawn from the Mississippi piver.
After the introduction of spray canal operation, thermal affluent from the Station could be cooled by the following methods: open-cycle operation with !
a single or two-pipe diffuser, closed-cycle operation with spray canal and com-bination or partial op-n-cycle operation with spray canal and diffuser. 'a'h en operating in combination cycle, approximately 1182 efs (53%) of the cooling water is circulated through the spray canal while 1048 (47%) of the water is discharged through one or both of the diffuser pipes. Make-up water is equal to the amount r of water discharged through the diffuser system. The flow of cooling water through the Quad Cities Station during the various modes of operation is pre-sented in Figure 5. Table 1 presents the average monthly Station capacity factor ,
from August, 1972, through December, 1979. The Station capacity factor is de-fined as the power output over the maximum amount of power the Station is cap-able of producing and is expressed as a percentage. The monthly total Statien capacity factor varied between 6 and 92% over the eight year period of operation.
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PLUS PLANT SERVICE WATER DITrU3ER /
CPENCYCLE/ 9P 111 cfs ir1048 cfs BLOWDOWN 015 CHARGE I
" 2230 cfa DISCHARGE P',0$
PLANT SERVICE WATER r 3
- -4 r (ICSSISSIFFI RIVER _j Figure 5 riow of cooling water through the Quad-Cities Station, g 20
f i
TABLE 1. Monthly Capacity Factors a ,b, Quad Cities Station August, 1972 through December, 1979. .
Year j 1972 1973 1974 1975 1976 1977 1978 1979 l Month Capacity Factor January- -
Unit 1 77 60 25 4 81 94 27 Unit: 2 64 77 e 95 94 33 89 Total 71 69 12 50 88 64 58 ;
Tebruary Unit 1- 73 72 11 0 66 72 e
. Unit 2 78 76 c 68 63 c 79 Total 76 74 6 34 65 36 40 March Unit 1- 75 79 99 22 50 92 79 Unf.t-2 92 66 c 76 28 47 81 Total 84 73 45 49 39 70 80 April Unit 1 .51 c 93 70 e 59 90
-Unit 2 41 77 1 92 92 88 74 Total 46 39 47 81 46 74 82 May Unit 1 45 a 62 70 40 64 68 Unit 2 64 83 72 80 79 61 -82 Total 55- 42 67 .75' - 60 62 75 l June Unit 1 82 c 81 49 70 72 94 Unit 2 86 39 74 70 77 54 79 Total 84 20 78 59 74 63 86 July Unit. 1 86 11 74 29 72 83 94 Unit 2 79 78 65 .72 6% 86 75 50 67 84 84 Total 82- 45 69 .
I
_ August i Unit 1 48 69 82 67 54 38 88 89 38 67 44 95 62 Unit 2 . 39 76 84
-44 53 61 41 92 75 Total 73 83-September-60 88 78 87 30 79 55
. Unit 1 57 44 66 23 48 87 51 Unit 2 c 69 Total 28 65 66 72 55 39 83 53 October.
O Unit 1 68 68 49 74 8
82 e
51 70 71 83 97 51
. ' Unit 2 32 70 75 62 41 41 64 77 74 Total- 50- 69 21
. .-- ca .n - ._ . . . - - _ . ~ _ . , . - . . _ . . . - . . _ . . . _ --. , .. ...._ .,_a _ . _ , ,,.u - _.. _ m ,._. _ ~
TABLE 1. (continued)
Year 1972 1973 1974 1975 1976 1977 1978 1979 Month Capacity Factor November Unit 1 74 70 77 67 66 79 65 90 Unit 2 73 62 74 60 67 64 83 37 Total 74 76 76 63 67 71 74 63 December Unit 1 76 84 84 62 87 81 64 68 Unit 2 69 86 46 91 75 79 90 c Total 73 85 65 76 81 60 77 34 O
abased on daily average power outpuc as determined by Co=monwealth Edison Company.
bTotal Station Capacity = 1618 5'e. h cUnit inoperative.
22
O The physical aspects of Station operation have been monitored on a daily basis since August, 1972. These data are presented in the reports en-titled " Operational Environmental Monitoring in the Mississippi River near Quad Cities Station" (Industrial Bio-Test, 1972, 1973a, 1973b, 1974a. 1974b, 1975; NALCO Environmental Sciences, 1975, 1976a, 1976b, 1977a, 1977b, 1978a, .
1978b;'Hazleton Environmental Sciences, 1979a, 1979b; Environmental Research and Technology, 1980). These data include temperatares taken. upstream of the -
plant (river ambient), at the Station intake, at the return side of the spray canal, at the discharge and downstream of the discharge. TF . reports also r
present a-chronology of Station operation which includes a record of the number l of lift' pumps operating to the spray canal, the number of operating circulating d
water pumps and the mode of Station operation (open, closed or combination ,
~
cycle cooling). Monthly minimum, maximum and mean water temperatures at the Quad Cities Station are presented in Table 2.
.f
[
O 23
_ __ , ,. _ - . . ., _ _ . _ _ _ _ ..-. _..._ _ -_ . . _ .,_ _ _ _ _ . _ . ~. _ __ __.- -
MM 7w ;- ,
J TABLE 2 l
Monthly Minimum, a s sivum and Mean Water Temperatures (*F) at the Quad Cities Station, August, 1972 Throcgh December,1979 Discharge Downstream Upstream Intaken _ _
Mean Max. Mean Min. Max. Mean Min._ Ma>_
Year Month Min. Max. Kean Min.
68.5 83.0 72.9 70.0 100.0 85.1 68.0 83.5 75.2 1972 August 67.5 83.0 68.5 61.5 95.5 75.4 58.0 75.8 68.9 58.0 75.5 68.3 58.0 74.0 67.8 45.0 60.0 52.4 September 42.0 59.5 51.7 50.0 73.5 63.7 October 44.5 59.5 51.8 45.0 76.5 63.8 33.0 48.0 40.4 November 33.1 46.9 40.0 33.6 53.2 40.7 79.5 66.4 32.0 35.5 33.5 32.0 69.5 35.1 32.0 D ember 32.0 34.0 32.3 32.0 46.6 32.4 41.0 76.0 59.4 32.0 34.0 32.4 1973 Janinry 32.0 32.5 32.1 45.5 68.0 58.3 32.0 36.0 33.1 February 32.0 34.0 . .4 32.0 34.1 32.4 74.0 64.4 33.6 46.8 41.4 33.4 46.5 41 3 51.5 March 33.6 46.5 41 56.0 74.0 64.2 38 5 58.4 49.3 April 38.5 58.0 4 ': J 38.5 65.0 48.0 83.9 74.1 53.B 64.4 58.9 l 54.0 63.7 58.8 56.8 May 54.0 63.7 74.7 100.0 93.2 63.5 80.5 74.1 63.6 80.5 /J.9 53.7 81.0 74.0 74.1 84.4 79.3 l
June 73 9 82.8 78.1 73.8 82.8 78.1 86.2 101.4 97.4 laly 72.9 101.5 93.7 71.7 nt.4 77.6 l
71.4 80.2 72.1 71.5 80.5 76.7 62.C 62.1 70.2 August 61.2 80 7 69.3 $1.5 80.7 69.4 71.5 100.0 87.9 September 64.0 87.0 77.1 50.7 66 9 60.4 October 50.1 65.6 59.7 50.3 65.9 59.7 72.4 63.0 37.6 52.0 42.9 37.4 50.1 39 . '- 50.5 November 39.0 50.1 42.1 51.0 65.1 57.3 32.0 41.4 34.4 g
- ' December 32.0 41.1 33.6 32.0 41.1 33.6 32.0 32.9 32.1 32.4 62.4 53.5 32.0 35.5 32.7 1974 January 32.0 32.8 32.1 50.8 58.9 56.3 32.0 15.6 33.5 32.0 33.7 32.3 32.0 33.8 32.3 32.5 40.8 37.6 February 31.9 4C.0 37.2 33.7 63.4 57.3 March 31.9 39.6 37.2 47.0 78.3 63.2 38.9 61.1 49.4 33.8 60.1 49.2 38.9 60.3 49.3 53.1 68.0 58.5 April 52.8 68.5 50.3 64.5 99.9 79.2 May 53.0 67.2 69.0 66.3 109.0 79.5 65.4 74.5 70.1 65.5 73.5 65.1 65.4 73.6 69.9 73.8 85.0 80.2 June 73.9 83.3 79.6 74.7 108.9 98.9 July 74.1 83.3 78.5 85.4 112.1 105.9 68.5 80.6 75.4 69.0 78.4 74.6 69.0 78.2 74.5 58.5 74.6 64.1 August 58.5 73.2 65.9 58.5 72.0 65.5 72.0 109.9 89.0 September 49.5 61.5 53.0 54.0 111.0 86.1 49.3 59.3 54.9 October 49.5 57.8 54.4 55.0 104.1 32.7 33.4 39.7 45.0 33.8 72.0 44.4 33.8 73.0 44.5 32.0 36.9 33.9 November 32.0 69.8 33.1 32.0 64.0 33.2 42.0 105.0 68.0 December 32.0 33.1 32.1 32.0 50.2 36.1 32.0 34.3 32.4 1975 January 32.0 13.3 32.1 32.0 55.8 34.8 32.0 32.4 32.1 February 32.0 38.0 32.0 32.0 32.5 32.0 74.5 58.9 32.0 35.5 33.3 32.0 35.2 12.9 41.5 brch 32.2 35.2 33.1 .0 47.7 85.0 63.3 33.0 52.5 44.0 pril 32.9 52.0 43.9 33.0 52.1
< -- IM
< .. x . -
3 7-O- O O TABLE ? teaca u" -.
Upstream Int _
Discharge _
Downstream Min. Max. Mean- ;
Min. Max. Mean -Min. Max.. Mean Year Month _Min. Max. Mean 50.4- 73.* 69.9 50.5 75.6 63.7 69.2 115.0 99.0 53.0 74.3 62.6 3975 lby June 66.0 82.4 73.2 60.0 82.5 73.6 93.0 l'L3.0 103.6 66.4 84.1 73.7 <
July 73.01 84.5: 79.5' 73.0 84.5 79.9 85.6' li' t 103.7 72.9 85.5 80.0 August 72.3 84.0. 77.8 72.1 37.5 78.3 81.5' 114 96.2 72.4 85.5 178.4.
58.6 76.8 66.1 58 + 77.1 66.1 76.5 100.0 89.6 58.6 78.1 66.1 September October 51.0 63.1' 57.5 53.5 72.4 63.1 76.2 109.0 88.7 50.5. 63.5 57.8 ,
i November 34.0 55.0 46.0 37.0 63.0 50.5 60.0 115.4 93.5 34.4 56.5 46.5' !
December 32.0 37.9 32.7 26.6C 52.0 41.2 81.8 111.5 101.6 32.0 .38.0 33.0 ,
l 32.0 32.2 32.0 32.0 52.0 40.1 67.5 107.5 83.7 32.0' 32.4 32.0 ,
l 1976 January 32.0 38.9 33.3 33.5 45.0 40.6 32.0 99.4 73.3 32.0 37.6 32.8 1 February .i 32.5 49.7 39.5- 33.5 59.5 47.1 71.0 108.5 86.7 33.3 49.9 39.6 March April. 43.9 60.0 53.0 47.0 77.0 62.3 80.0 120.5 109.2 43.7 59.4 51.2 May 53.1 69.5 -62.0 59.5 79.2 69.1 88.4 120.1 110.3 53.5 69.9 64.4 67.8 79.1 73.6 71.0 S6.3 76.6' 80.0 113.6 99.5 67.2 80.2 74.3 :
June
- 70.2 82.8 78.6 72.0 87.0 80.1 89.0 111.0 99.0 72.1 84.9 79.3
.tuly 72.6 79.6 76.3 72.6 83.6 77.1. 83.5 108.5 98.2 73.1' 81.3 77.0 August 62.0 74.7 67.0 60.0 75.0 67.1 b b b 60.1 76.3 67.4-w September
- 43.5 63.4 31.1 53.9 96.6 79.2 44.0 65.1 52.8 October 43.6 63.5 52.2 l'
November 32.2 44.4 36.5- 32.1 44.8 36.6 43.0 84.9 67.9 32.3 46.7 38.2 December 32.0 38.0 32.5 '32.0 59.7 44.0 52.6 115.0 88.5 32.0 37.5 34.1 1977 January 32.0 32.3 32.0 32.0 58.9 37.6 63.5 113.0 83.2 32.0 38.9 33.7 February 32.0 36.5 32.3 32.0 57.7 34.3 53.5 98.6 70.7 32.0 36.7 33.8
' 32.0 49.6 37.5 32.0 49.6 41.2 43.0 100.9 77.6 32.2 49.6 37.8 March-43.8 66.3 56.1 43.8 66.2 56.1 66.5 104.8 89.1 44.3 68.4 56.7 April i lby 61.1 79.3 70.4 61.0 87.3 70.6 83.3 111.0 95.7 61.3 80.9 72.8 68.3 82.0- 74.6 83.9 100.7 100.0 67.4 84.7 74.7 June July 67.5 75.9 82.2 85.0 73.9 80.0 73.1 8f.5 81.0 84.4 -116.5 104.0 75.9 87.0 81.3 l August 67.0. 78.2 74.5 67.1 66.0 77.6 79.5 107.0 96.2 67.3 80.7 75.2 ,
September' 61.9 74.9' 67.6 74.3 S0.3 72.6 88.0 112.7 102.5 62.1 77.0 68.1 49.3 6G.9 60.5 55.7 112.4 97.1 49.4 60.3 52.3 October 49.2 59.7 52.0 November 32.0 53.5 43.0 40.5 63.6 52.9 52.6: 108.7 95.6 32.0 54.4 43.1 j 78.8 112.5 98.6 32.0 38.9 32.7 l December 32.0 33.4 '32.3 32.0 60.8 43.7 I
, , , ...,e . ~ . .- . , , .
TASLE 2 (continued)
Upstream Intake 8 Discharge Downstream Mrx. Mean Min. Max. Mean Min. Max. Mean Min. Max. Umn, Year Month !!in.
32.0 32.0 32.0 32.0 56.3 38.2 60.6 114.0 89.2 32.0 35.7 32.8 1978 January 32.0 32.0 32.0 32.0 51.7 32.4 32.9 99.5 74.3 32.0 35.3 32.6 February March 32.0 36.2 32.5 32.0 38.6 32.6 34.0 92.0 61.4 32.0 41.1 33.0 April 32.7 51.7 47.3 32.5 71.5 52.5 58.8 107.1 88.1 32.0 52.2 47.6 May 50.6 74.4 60.3 53.5 77.1 64.0 80.3 113.2 103.5 50.6 75.5 62.6 70.3 79.8 73.3 70.1 80.2 74.8 85.4 110.0 99.9 68.5 80.0 73.3 June July 73.0 81.5 77.4 70.5 82.5 76.2 94.8 118.9 107.3 73.0 82.7 77.9 August 73.3 80.2 76.4 71.0 81.6 75.5 101.0 112.0 107.9 73.0 81.6 77.2 September 62.2 79.8 72.0 59.8 81.0 71.4 91.2 111.8 103.1 53.3 81.9 72.0 October 48.3 62.2 53.8 48.7 68.7 58.1 86.0 111.2 100.5 47.2 65.0 54.4 32.2 51.9 41.2 32.0 62.3 46.5 74.2 119.8 107.8 32.0 53.8 41.1 November December 32.0 33.8 32.3 32.0 68.3 48.4 80.8 119.9 103.6 32.0 37.5 32.4 32.0 33.5 32.0 32.0 70.0 39.4 40.2 120.0 87.5 32.0 35.0 32.3 1979 January 32.0 32.8 32.1 32.0 67.5 36.2 51.3 106.8 80.3 32.0 33.7 32.1 February 32.0 38.7 32.7 32.0 61.5 37.2 64.2 106.8 85.9 32.0 38.2 32.7 Furch 34.3 54.1 44.3 April 34.2 54.9 42.8 34.6 56.6 45.4 64.8 100.5 87.5 52.5 63.9 62.8 48.8 70.0 61.0 67.5 107.0 92.0 49.5 68.4 60.9 May June 67.2 78.5 72.6 66.2 79.8 72.5 93.5 101.9 101.1 66.7 76.8 72.4 ra July 74.0 81.9 78.0 72.8 81.9 77.8 110.0 117.5 106.7 73.6 82.6 78.5 70.2 81.8 76.0 69.3 82.1 75.5 78.2 119.5 102.8 67.5 82.9 75.3 August 63.5 77.5 69.8 C 65.0 85.0 72.4 September C 48.2 65.1 52.9 48.0 65.1 54.b 76.5 92.7 84.9 4s.o 67.5 54.3 October 35.0 54.5 43.2 33.6 50.3 41.7 63.4 95.7 82.6 33.3 52.4 41.6
!!ovember 32.0 36.4 33.3 31.7 39.1 33.4 32.0 92.8 68.1 30.3 35.3 33.4 December a lemperatures were recorded by a sensor located approximately two feet above the bottom.
b Data was not collected because of construction.
C Sensor inoperative.
8 9 e
. . _- ---- - _ _ _ _ _ - _ . .-~ . _ - . . - _ - - . .
2
=
Literature Cited Environmental Research and Technology, 1980. Operational Environmental Moni-toring in the Mississippi River near Quad Cities _ Station, August, 1979 through January,1980.
Hazleton Environmental Sciences, 1979a. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station, August, 1978 through January 1979.
, 1979b. Operation Environmental Manitoring in the Mississippi River near Quad Cities Station February,1979 through July,1979.
Industrial BIO-TEST Laboratories, 1972. Determination of Thermal Effects in the Mississippi River aear Quad Cities Station January through July, 1972.
, 1973a. Thermal Effects Studies near Quad Cities Station, August, 1972 through January,1973. -
, 1973b. Operational Environmental Monitoring in the }Hssissippi River near Quad Cities Station, February through July, 1973.
, 1974a. Operational Environmental Monitoring in the dississippi River near-Quad Cities Station, August, 1973 through January, 1974.
,-1974b. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station, February through' July, 1974.
, 1975. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station, August, 1974 through January, 1975.
NALCO Environmental Sciences, 1975. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station, February through July, 1975.
. 1976a. Operational Environmental Monitoring in the Mississippi-River near Quad Cities Station August, 1975 through January, 1976.
, 1976b. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station,' February through July, 1976.
, 1977a. Operational Environmental Moni:oring 1n the Mississippi River near Quad Cities Station, August, 1976 through January,-1977.
, 1977b.--Operational Environmental Monitoring in the Mississippi River near Quad Cities Station, February through July, 1977.
, 1978a. -Operational Environmental Monitoring in the Mississippi River near-Quad Cities Station, August, 1977 through January,1978.
() , 197Bb. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station, February through July, 1978.
27
O Section 11 316(a) Demonstration Supplement O
O
. . . - . - - . - - .... . . . . - . - . _ . . ~ . . .. . ...._. _...... -.. . -
O
~
Table of Contents Title g A. Hydrological'and Thermal Investigations 28 B. Summary of Biological Monitoring Studies 96 C. Ef f ects of Inct.ased +
Temperatures on Fish 117 I-l O
I f'
i.-
LO 1
t 6-. , -- 4 . - - w.-- .-,b, -.v ,, ...e.,,, -.,,,,,E,,,.,,ww-,e,,.7..,,w_,n,_n, 3,-%,-,,,-ye,,wy, %.,-g.r---m,, y .-y,, ,.
,,,-r, e v---w.- r5 -
O A. liydrological and Thermal Investigations O
O l
l
t i
b 9
1.. Critical Flow and Water Temperature Conditions i
for the
~ Mississippi River at Quad Cities Nuclear Station T
by Dr. P. K. K3tanidis l-l l
l i
I- ,
O
, , . _ , - . ._ . _ , . _ , , _ , _ . . . . . - , ...,.m.. =,.y.., ,,v. . . . , _,. , ., , -. ,
l O
Table of Contents Title Pg Critical Flow and Water Temperature Conditions for the Mississippi River at Quad Cities Nuclear Station 28 List of Figures 11 List of Table.s 111 I. Description of the Upper Mississippi River 28 II. Stream Flow of the Mississippi River at Clinton, Iowa 30 III. Temperature Data, Mississippi River in the Vicinity of Quad Cities Nuclear Station 41 IV. Mississippi River Temperature at Fulton, Illinois 47 V. Evaluation of the River Heat-Assimilation 47
-VI. Bibliography 56 f
i e
i i
~ .. . - . . _ . . .
I-J. .:
Table of Figures Figure No. Title Page 1 Annual Discharge of the Miosissippi River at Clinton 32 2 Annual Lowest Daily Discharge of the Mississippi River at Clinton 34 ,
3' Annual Lovest 7-Day Discharge of the Mississippi River et Clinton 35 4 Duration Curves of Mean Daily Discharge, thesissippi River at Quad Cities Nuclear Station 37 5 Duratdr . Curves. of Me.an Daily Discharge on Moathly Bases, Mississippi River at Quad Cities Nuclear Station 38 6 Duration Curves of Daily Discharge,
()' Mississippi River at Clinton Position of the Temperature Gage 39 43 7
8 Average Mississippi River Water Temperature during the Climatic Year 50 9 Duration Carve of Daily Temperature of Mississippi-River at Fulton 51 10 Duration Curvas of Daily Temperatare of Mississippi River at Fulton 52 11 Duration Carves of Daily Temperature of Mississippi River at Fulton 53 12 Duration Durve of Heat Assimilation Capacity of Mississippi River at the Quad Cities Nucicar Station 55 O
11
O List of Tables Table No. Title Pg 1 Seasonal Distribution of 7Q10, Mississippi River at LeClaire and Clintan (without Wapsipinicon River) 33 2 Seasonal Distribution of 7-day, 10-Year Low Flows, Mississippi River at Quad Cities Nuclear Station (including the Wapsipinicon) 36 3 USGS Water-Temperature Stations Along Mississippi River between Fulton and Quad Cities Nuclear Station 41 4 Temperature Increase Along the Mississippi River between Fulton and Quad Cities Nuclear Station 45 5 Comparison of Temperature Measurements at Fulton with Temperature Measurements just Upstream of Quad Cities Nuclear Station 47 6 Maximum Permissible Temperatures at Fulton 49 9
111
Critical Flow and Water Temperature Conditions for the Mississippi River at Quad Citics Nuclear Station1 I. Description of the Upper Mississippi River (above Lock and Dam 14). The tussissippi River rises at Lake Itasca in north-central Min-nesota and flows in a general southeasterly direction to Lock and Dam 14 which is situated a short distance upstream f rom the Quad Cities of Moline and Rock Island Illinois, and Bettendorf and Davenport, Iowa. Major tribu-taries in this reach include the Minnesota River in Minnesota; the St. Croix River in Minnesota and Wisconsin; the Black, Chippewa and Wisconsin Rivers in Wisconsin; and the Turkey, Maquoketa and Wapsipinicon Rivers in Iowa.
The topography of the basin consists for the most part of rolling farmland, except in the upper parts of the basin in Minnesota and Wisconsin where forests and lakes abound.
O Six Federal dams and reservoirs, built during the period 1884-1913, are located in the headwaters area above the mouth of the Minnesota River. The total storage capeity of these reservoirs between their operating limits is somewhat less than one million acre-feet (1)*. The reservoirs were constructed to provide supplemental flow for navigation needs of the Mississippi River during periods of low runoff. Since the completion of the system of locks and dans on the Upper Mississippi River in 1938 (1), regula-tion of the reservoirs for navigation needs is no longer of primary importance, and they are now operated principally for flood control, recreation, and related purposes (2).
1 Prepared by Dr. Peter K. Kitanidis, Institute of Hydraulic Research, The University of Iowa, Iowa City, Iowa.
- Numbers is parentheses refer to ite=s listed in the bibliography at the end of this report.
28
Flow in the Wisconsin River is regulated by 23 reservoirs and several hydroele:tric power plants. Usable storage in the reservoir system is approximately 29 billion cubic feet (666,000 acre-feet). Five of these reservoirs, with total storage of 337,000 acre-feet, have gone on line since 1935. Most of the others have been in use since ::he early 1900's. The reservoirs usually are drawn down for the late fall and winter periode and restored to normal pool levels n the spring freshet season.
Nine reservoirs, having a total storage of about 528,000 acre-feet, have been constructed along the Chippewa River basin in Kisconsin. Two of these, with total storage of 364,000 acre-f eet, were completed in the mid-1920's. The others were completed between 1880 and 1917.
During the 1930's, 13 locks and dams were constructed on the Upper Mississippi River between St. Paul, Minnesota, and Clinton, Iowa, in connec-tion with the 9-foot navigation channel project. Clinton is approximately 12 miles upstream from Quad Cities Station, which is situated along the River between Dams 13 and 14. These locks and dans are operated by the United States Department of the Army, Corps of Engineers. The navigation dams maintain nearly constant pool elevations during low and medium low flows. During these periods, the movable gates in the. dams .:re set so that there is a small (about 2 or 3 feet) opening between the botte.ns of the gates and the gate sills.
During medium and high flows the gates are taken entirely out of the water (1).
It is general operating practice to draw the pool above each navigation dam down about one foot at the close of the navigation season. The usual period of navigation closure by ice is from about December 1 to April 10 (1). Durins severe winters, however, navigation can be stopped as early as November 10, O
29
. - -- - _.-.. . - . . . - - . . . . ....- - . -_ .- - . _ ~ . . -
and may not be resumed until late April. The flow regulatiun incident to closure of the navigation season has had a significant effect upon the low-flow regime of the Mississippi River at Clinton, as will be discussed subsequently.
II. Streamflow of the Mississippi River at Clinton, Iowa. U.S. ,
Geological Survey streamflow records are available for the Mississippi River reach of interest at Le Claire ar.d Clinton, Iowa (497 and 512 miles above the Ohio River, respectively), for the period 1873 to date. Prior to 1939, the gaging station was located at Le Claire. Because of backwater caused by .
Lock and ram 14 at Le Claire, the gaging station was transferred to Clinton in 1939. The drainage area above Le Claire is approximately 88,600 square
-miles. The watershed of the Wapsipinicon River, which enters the Mississippi between the two stations, accounts for most of the difference.
('
The temporal distribution of river flow is distinctly seasonal.
Annual'high flows usually occur between April e"d June, and the annual low flows occur between December and February. The highest annual flow at Clinton (95,000 cubic feet per second (cfs)) occurred in 1882, and the lowest (18,500 ecfs) in 1934. The minimum daily flow of record,-6,500 cfs, occurred December 25-27, 1933. The average' flow for the period 1874 through 1939 is 47,700 cfs, and for:the period-1940 through 1977 is 46,400 cfs. The average flow of the Wapsipinicon is 1,400 cfs, accounting for the difference between the average flows for the two periods, as noted in-the preceeding paragraph.
Water pollution control agencies in Iowa and Illinois both use the 7-day, 10-year low flow (denoted by 7Q10) in the application of water quality O
30
~_ . . .~. _._-._. - . - . _ . . _ . . , . - _ - . . _. . . _ -- _ _ . - - _ _ _ . . .
criteria. This is the lowest average flow for 7 consecutive days that occurs with an a<crage frequency of once every 10 years. Stated another way, it is the 7-day-averaged low flow that has a 10 percent probability of not being exceeded in any year. Because of the significance of this discharge, an analysis was made to determine if significant changes in tiie low-flow regime of the River have occurred as a result of increased development of the main stem and tributaries.
The 7-day, 10-year low flow at Clinton (Le Claire) for several periods is as follows:
Period prior to navigation dams (station at Le Claire)
(climatic years 1875-1939) . . . . . . . . . . . . 9,000 cfs Period after navigation dams (station at Clinton) ,
(climatic years 1940-1977) . . . . . . . . . . . 13,400 cfs This tabulation shows that 7Q10 was significantly greater in the recent 39 years than in the preceeding 62 years, even though the average flew for the recent period (46,400 cfs) was less (see Figure 1) than that for the 64-year period (47,700 cfs).
By summing the flow of the Mississippi River at Clinton and the flow of the Uapsipinicon River (as measured by the USGS near DeWitt, Iowa), 7Q10 for the period 1940-1977 was found to be 13,700 cfs at Quad Cities Nuclear Station.
Note that the value is slightly larger than the 7Q10 of 13,200 cf s for the period through 1969 used by Kennedy and Jain in the diffuser-system analysis.
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Since 1940, the minimum annual daily flow at Clinton was less than 10,000 cfs in only one year (9,600 cfs in December 1976), Between 1875 and 1939, the minimum annual daily flow was equal to or less than 10,000 cf s in 12 years (Figure 2). The miniers recorded 7-dsy low flew was 9,000 cfs in the period 1940-1977, and 7,400 cis in the period 1875-1939 (Figure 3).
One of the factors contributing to the substantial increase in 7Q10 in the recent period is the seasonal navigation-pool drawdown, which coincides with thn period when most low flows occur. Thus, storage from the system of navigation pools is released to augment natural flows during a critical period each year. In the period prict to operation f the navigation dams, most of the annual 7-day flows occurred in the month of Dece=ber. Since 1940, however, the distribution of thq occurrences of the annual 7-day low flow has changed drastically. Now they are f airly well distributed in the period between August and February. On a seasonal basis, 7010 is as given in Tabic 1.
Period 7Q10 (cfs)
October-December Period 1875-1939 (Le Clcira) 9,700 Period 1940-1977 (Clinton) 14,500 January-March Period 1875-1939 (Le Claire) 11,200 Period 1940-1977 (Clinton) 14,500 April-June Period 1875-1939 (Le Claire) 24,900 Period 1940-1977 (Clinton) 22,700 July-September Period 1985-1939 (Le Claire) 16,000 Period 1940-1977 (Clinton) 14,500 Table 1. Seasonal distribution of 7Q10, Mississippi River at Le Claire and Clinton (without including the Wapsipinicon River) 33
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O The flow at Quad Cities Nuclear Station is the sum of the flow of the Mississippi River at Clinton with the flow of the Wapsipinicon River at DeWitt.
The quantity 7Q10 of the Mississippi River at the Station for the period 1940-1977 is given in Table 2.
Period 7Q10 (cfs)
October-December 14,700 January-March 14,700 April-June 23,200 July-September 14,900 Table 2. Seasonal distribution of 7-day, 10-year low flows, Mississippi River at Quad Cities Nuclear Station (including the Wapsipinicon River).
Flow-daration curves, which show the percent of time that indicated O discharges have been equalled or exceeded, are a convenient means of illus-trar.ing the entire flow regime for a particular period of record. Flow-duration curves for mean daily discharge of the Mississippi River at Quad Cities Nuclear Station are presented in Figure 4 on annual and seasonal bases and on a monthly basis in Figure 5. The flou-duration curves for the Mississippi River at Clinton (Figure 6) confirm that low flows for the period since 1940 are substantially higher, and medium and high flown somewhat lover, than those for the period prict to 1940. The reasons for this are set forth above.
As pointed out above, about 337,000 acre-feet of usable storage has gone on line in the Wisconsin River basin since 1935. Two of the largest of these reservoirs--the dans on the Petenvell and Castle Rock Flowages--
were placed in operation in 1950. Analysis of flow records for the period
() since 1938 have indicated that storage releases in the Wisconsin River basin 36
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are the principal causes of increased Mississippi River flows in January and February. Storage releases from the navigation pools on the main stem have the greatest effect on flow in early winter.
In order to detemine whether the period since 1940 is representatise ,
of a longer-tem period, flow-duration and 7-day low-flow frequency curves for the Cedar River at Cedar Rapids, Iowa; Pecatonica River at Freeport, Illinois; and La Crosse River near West Sale =, Wisconsin, were studied. Records at these stations extend back to 1902, 1914, and 1913, respectively. Analysis of these records indicated that there is practically no difference between the flow i- patterns for the long-tem periods and the period since 1940. If these dis-charge records for these other sites are representative of the Mississippi River basin between St. Paul and Clinton, then the record at Clinton since O
V 1940 should also be representative of a long-tem period. It was concluded that this is indeed the case.
The combination of the operation of a series of navigation dams on the main stem and developuent of storage reservoirs in the Wisconsin River basin have materially altered the low-flow regime of the Mississippi River at Clinton. Since these control structures will continue to function for the foreseeable future, the flow selected for application of water quality criteria should be based on the period of record since 1940. . Based upon the analyses discussed here, 7Q10 for the Mississippi River is 13,400 cfs at Clinton and 13,700-cfs at the Quad Cities Nuclear Station, as determined from the low-flow frequency curve for the period since 1940.
< O 40
III. Temperature Data, Mississippi River in the Vicinity of Quad Cities Nuclear Station.
A. Description of Stations. The U.S. Geological Survey operates three continuous-record weter temperature gaging stations on the FEssissippi River within 20 miles of the location of Quad Cities Nuclear Station (506 miles upstream f rom the Ohio River, or R.M. 506). The exact locations of the data-acquisition points and the lengths of river-temperature records are given in Table 3.
Station Name Number, River Mile Length of Record Clinton, Iowa 05420500 518 1974-1977 Hampton, Illinois 05422400 493 1973-1978 (Dam 14) .
Fulton, Illinois 05420400 522 1969-1978 (Dam 13)
Table 3. USGS vater-temperature stations along Mississippi River near Quad Cities Nuclear Station.
Other USGS continuous-record water temperature gaging stations on the Mississippi River are at McGregor, Iowa (R.M. 633.4', Keokuk, Iowa (R.M.
364.2), Alton, Illinois (R.M. 202.7), Kellogg, Illinois (R.M. 201.9) and Chester, Illinois (R.M.176.8) . However, due to their relatively large dis-tances from the Station, these data were not used in the analysis.
- 1. Clinton, Iowa: This site is 12 miles upstream from Quad Cities Nuclear Station. Due to certain problems, opera-tion of the temperature record was discontinued in 1977. Temperature data for 1978 were collected at the 41
Fulton station at Dam 13 (station no. 05420400). For the period of-record-(watet .ar 1974 to 1977), tempera-ture was usually recorded once daily.
- 2. Hampton, Illinois: This site is 13 milen downstream from Quad Cities Nuclear Station. The records are not complete, with some data from the most cr17.ical p<rL> (April and summer months) missing. Hewever *.he p.eriods of record coincide with the period Quad Cities Nuclear Station was in operation, and consequently the water temperature at this location has been influenced by the thermal discharges from the Stttion.-
- 3. Fulton, Illinois: This site is apprcximate?.y 16 miles up-stream from Quad Cities Nuclear Stat: ton. A temperature
/%
V-recorder has been in operation there . since June-1969. These measurements are considered to be more reliable than measure-ments taken at the Clinton or the Hampton station, and were used in the present analysis.
B. Verification. The temperaturo recorder is located at Lock and Dam No. 13 (R.M. 522.5). Its exact location is indicated by an asterisk in Figure-7. Before analyzing the records one must establish that the records Jare representative of the ambient River temperature in the vicinity of Quad Cities Nuclear-Station. -Thermal r,tratification as well as . lateral and longi-
'tudinal variation of.temperatura must be examined.
O 42
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, 1. Stratification characteristics: With the exception of q
(_s/ ' the slough arcas, which may exhibit thermal stratifica-tion during the summer months, practically no stratifi-cation occurs in the River in the vicinity of the Quad Cities Station (3, 4). Thus, although the temperature is measured at a depth slightly below the low-flow pool, 1
the recorded values should give a good estimate of the )
depth-average temperature even in periods of low flow.
- 2. Lateral (across the River) variation: Temperature dif-ferentials across the Mississippi-River are often pro-nounced.Ibecause -f the large width of the River and the
. slow rate of lateral mixing. This variation makes eval-uation of the average cross-sectional ambient temperature e
rather difficult.
- 3. Strea= wise temperature increase: The average temperature of the Mississippi River water increases as the water moves downstream. This is the result of the variation of am-bient air temperature and solar radiation associated-with the change of latitude, and also a result of mixing with the generally wa mer water of the tributaries.
The natural (no plants operat1ng) temperature increase along'the Mississippi River betcaeen Fulton gaging station,.
a wnere data are available, and Quad Cities. Nuclear. Station has been estimated using a computer-based numerical model (3) for average River discharge and weather conditions, with the results given in Table 4. The calculated natural O
44 k' - , _ _ . _
(no plants operating) temperature increase for 7Q10 ccm- h bined with everage weather coniltons is also given in Table 4.
Month AT AT (for e7e' rage Q) (f or7Q10)
F,bruary 0 'T 0 'T May 0.2 'T (not ava14able)
August 0.1$'T 0.20*f November 0.2 *F 0.15'r Table 4. Temperature increase along the Mississippi River between Fulton and Quad Cities Nuclear Station.
With the existing plants the temperature increase between Fulton and the Station is smaller than the cor-responding natural increase, h The Wapsipinicon River flows into the Mississippi River uownstream of the Fulton gaging statiot and a short distance upstream of the Station, and probably accounts for the hrgest part of the water-tempers'ure increase between the two locations. The mean flow of the Wapsi-pinicon at DeVitt. Iowa, is less than 4 percent of the mean flow of the Mississippi River at Clinton. On the basis of USGS data from gaging stations on rivers with drainage areas, topography, and geographical settings similar to those of the Wapsipinicon River, it was es-tablished that one should expect the temperature of 9
45
1 O
the Wapsipinicon River to be within 14'T of the tempera-ture of the Mississippi River at the point of confluence.
Consequently, for average flow conditions, the Vapsi-pinicon River should not affect the average temperature in the Mississippi River by more than to.16'T. This effect abould be even smaller in the case of the low flows, since the contribution of the Wepsipinicon River to the Mississippi River 7Q10 at the Quad Cities Nuclear Station is less than 3 percent of the Mississippi River discharge.
Temperature measurements from the Fulton station vere compared with some temperature measutements taken just upstream f rom Quad Cities Nuclear Station. The results of this comparisen are presented in Table 5. It is seen that for all dates for which data vere available the Cirference between the temperature 'thich has been recorded at Fulton by the USGS and the temperature which has been recorded just upstream f rom Quad Cities Nuclear Station by the Iowa Institute of Hydraulic Research and Hazleton Environmental Sciences Corporation (formerly NALCO Environmental Sciences) is within the anticipated (3, 4) lateral (ncross the River) temperature variation.
O 46
Daily Average Average Ambient Daily Average Temperature Temperature at Temperature at Recorded at Quad Cities-- Quad Cities--
Date Fulton IIRR Measurements HISC Measurements
('F) ('F) (*F) 11-02-72 44.5 46.5 11-09-72 42.5 44.1 11-28-72 32.5 34.5 07-23-73 75.0 74.5 07-25-73 76.5 78.0 07-31-73 75.5 77.5 08-17-73 77.0 79.0 08-30-73 78.0 80.0 09-12-73 67.5 71.0 10-1B-73 61.5 63.0 10-31-73 48.5 51.5 11-14-73 40.0 40.5 12-03-73 40.0 40.5 01-16-74 32.0 32.0 01-21-74 32.0 32.5 03-14-74 37.5 37.5 38.5 07-15-76 81.5 81.0 61.0 09-16-76 66.0 68.5 67.0 09-30-76 61.0 62.0 61.5 Table 5. Comparison of temperature measurements at Fulton with temperature measurements just upstream of Quad Cities Nuclear Station.
O 47
.._ .-__m. . . . _ _ . _ _ _ . _ _ _ _ _ _ _ _ _ _ . _ _ _ _ _ _ . _ _ _ . . . .
IV. Mississippi River Temperature at Fulton, Illinois. The princi-pal temperature variations of the Mississippi River at this site are seasonal.
The average temperature during the climatic year is given in Figure 8. The j
]
i annus1-high temperature usually occurs in July. The highest daily temperature recorded in the period June 1967 to September 1977, 85'F, occurred in July t
l 1977. :
The percent of time a given temperature is equalled or exceeded at Fulton is presented in Figure 9. The percent of time a g4,ven temperature is equalled'or exceeded is presented in Figures 10 and 11 on a monthly basis, for
- the months April through September. The period of record used in the develop- l ment of these figures is June 1967 to September 1977. These figures indicate !
that an average 6eliy River temperature of 82'F is equs11ed or exceeded at Fulton-one percent of the-time on an annual basis.- However, the same tempera-ture is equalled er exceeded seven percent of the time during the month of July.
V. Evaluation of the River Heat-Assimilation Capacity. Water pol-lution control agencies in both Iowa and Illinois have adopted maximum tem-peratures which cannot be exceeded more -than one percent of the hours in- the - t 12 month period ending any month. These maximum permissible temperatures prescribed by Iowa and Illinois are given in Table 6. .
January 45 45
-February 45 45 March 57 57 ,
Aptil 68 68 l
l 48 l .. . ..
May 78 78 June 85 86 July 86 88 August 66 88 September 85 86 October 75 75 November 65 65 December 52 52 Table 6. Maximum permissible temperatures at Fulton.
The data summarized in Figures 10 and 11 indicate that the River temperature at Fulton does not exceed these limits more than one percent of the time. However in order to identify critical combinations of River dis- h charge and River temperature which may result in the violation of these stan-dards at Quad Cities Nuclear Station, the following analysis was performed.
The permissible heat-assimilation capacity of the river is defined here as the maximum rate of heat input which will not increase the River water temperature above the permissible maximum. This analysis does not address the question of whether the discharge of waste heat satisfies the other water quality standards, such as time-rate of temperature increase, mixing-zone characteristics, etc.
The heat-assimilation capacity of the Mississippi River at the loca-9 tion of the Quad Cities Nuclear Station can be calculated from the River i discharge and the permissible temperatire increase using the following formula:
O 49
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w T
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m w so .
O i w
d 50
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40 -
30 1 Apr. 1 Jul. 1 Oct 1 Jon TIME Figure 8. Average Mississippi River Water Temperature during the Climatic Year O
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{ %,* %,*-
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$ ' AUGUST t;
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40 -
30 0 01 0.1 05 1 2 5 10 20 30 40 50 60 70 80 90 95 98 99 99 9 9999 PERCENT OF TIME EOUALLED OR EXCEEDED figure 11. Duration Curves of Daily Temperature of Mississippi River at Fulton (on a monthly basis)
- O O
. _ _ _ _ . _ _ . _ _ _ _ _ _ _ _ _ _ _ _ . .. _ . _ m . . .__
O HAC = 62.4 Q(AT) where HAC = the heat-assimilation capacity (Btu /sec) of the :
Mississippi River at the location of the Quad l Cities Nuclear Station.
t Q = the River discharge (cfs) at the Station, cal-culated as the sum of the discharge of the Mississippi River at Clinton, and the discharge of the Wapsipinicon River at DeWitt.
AT = the maximum permissible temperature increase (*F),
given by 0 , IF T g - Ty - 0.2 <0 AT =_Tg - Tp - 0.2, if 0 <T g - Ty - 0.2 <5 5 , if Tg - Ty - 0. 2 >$
where T g is the maximum permissible temperature (*F) and Ty is the River temperature (*F) at Fulton. The correction term, 0.2*F, accounts for the
.O difference between the River water temperatures at Fulton, and Quad Cities Nuclear Station.
Using measured daily temperatures and discharges for the period June 1969 to-September 1977, and the Iowa water-temperature limits, adopted in the NPDES Permit,.the heat-assimilation capacity of the Mississippi River was statiscally analyzed. The percent of time a given HAC is equalled or exceeded is depicted in Figure 12. The heat-assimilation capacity of 3,200,000 Btu /sec, corresponding to the full load waste-heat discharge rate from Quad Cities Nuclear Station,-is equalled or exceeded 99.2 percent of the time. Conse-
-quently the data indicate that heated discharge from the Station, operating .
cor.tinuously at full load, will cause River-water temperature increases which are within the limits set in the NPDES Permit 99.2 percent of the time. When O
54
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O V the Stati.on operates continuously at half load, the maximum temperature limits ,
1 set in the NPDES Permit will be exceeded only 0.3 percent of the time.
In the period of record, the River heat-assimilation capacity has e
been less that 3,200,000 Btu /sec 21 times, all of them during the low-flow water year 1977. In the period of record the River heat-assimilation capacity c was less than 1,600,000 Btu /nec eight times, all of them in May 1977. Natural temperature exceeded the temperature limit adopted in the NPDES Permit two 1 times in the period of record, both in May 1977.
An analysis of actual plant operating data performed by Commonwealth
. Edison Company indicates that during the 21 times that the heat-assimilation capacity was less than 3.200,000 Btu /sec, the plant exceeded the temperature
. sr.andard a total of 77 hours8.912037e-4 days <br />0.0214 hours <br />1.273148e-4 weeks <br />2.92985e-5 months <br /> which is 0.9% of the hours in a twelve month O petiod. .At no time did the plant exceed the maximum allowable temperature which is 3'F above the monthly temperature standard.
i
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I O
56
O LIBLIOGRAPHY
- 1. Corps of Engineers, "The Riddle and Upper Mississippi River", 1940,
- 2. House Connittee Print No. 13, 89th Congress, let Session.
and Kennedy,
- 3. Jain, S.C., Sayre W.W., Akycampong, Y.A., McDougall, D.,
J.F., "Model Studies and Design of Thermal Outfall Structures. Quad Cities Nuclear Plant", IIllR Report No.135, Ir. titute of Hydraulic Research, The University of Iowa, 1975.
- 4. Commonwealth Edison Company, "Three-Sixteen e and b Demonstration -
Quad Cities Nuclear Station Mississippi River", A Demonstration to the U.S. Environmental Protection Agency, Chicago, Illinois, 1975.
Paily, P.P., Su, T.-Y., Giaquinta, A.R., and Kennedy, J.F.,
"The Thermal 5.
Regimes of the Upper Mississippi and Missouri Rivers",1111R Report No.
182, Institute of Hydraulic Research, the University of Iowa, 1976.
O O
57
G
- 2. Thermal and liydraulic Performance of the Quad Cities Nuclear Scation
- k'aste lleat Dif fuser System
- by Dr. J. F. Kennedy and Dr. S. C.-Jain l
I 1
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O Table of Contents Title M Thermal and Hydraulic Performance of the Quad Cities Nuclear Station Waste-Heat Diffuser System 58 11 List of Figures 111 List of Tables Introduction and Background 58 1.
- 11. Description of the Quad Cities Nuclear Station Diffuser System 62 111. Field Testing of the Quad Cities Nuclear Station Diffuser System 66 67 IV. Presentation of Results V. Further Detailed Analysis of Discharge through and from Diffuser-Pipe System 86 Globa)-Tield Perspective 91 O
VI.
Summary and Conclusions 93 V11.
Bibliography 95 VIII.
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i List of Figures O Title Pale, e
Figure No. [
1 Site of Quad Cities Nuclear l Station 61 i i
2 Layout of the Diffuser System ;
for Quad Cities Nuclear Power j Station 63 r 3 Plan and Sectional Views of the i CNS Diffuser System 64 t
4 Sectional View of Diffuser System l Manifold and Riser 65 5 Observed Temperature 200 ft Up- [
r Stream and 500 ft. Downstream from Diffuser System, 3 December :
1973 69 6 Measured temperatures 200 ft. Up-Stream from t.he Diffuser System before and after Downstream Measurements, 15 ,
July 1976 70 t i
O '7 Plant Temperature Rises and Velocity Measured 15 ft. Downstream from a i
Main-Channel Diffuser Pipe Port, 30 October 1974. 74 l 8 Minimum Zone of Passage with Respect ,
to Total River Discharge for the Case l
of Plant Operation at Full Capacity 76 !
9 Observed Point-Temperature Lises 500 ft.
Downstream from the Diffuser System, 3 December 1973 and 16 January 1974 79-
-10 Observed Tempertture Rises 500 ft.
l Downstream from the Diffuser System on 15 July 1976 80 11 Observed Temperature-Rise isotherms 500 ft. Downstream from the Diffuser System 81 on 15 July 1976 _
12- Maximum Temperature Rise 500 ft. Down- i Stream and Ambient Temperature 1000 ft.
Upstream from Diffuser System en 28 November 1972 83 4 O
e 11
. I 1
Figure No. Title Pm 13 Transverse Distribution of Depth-Averaged Temperature 500 ft.
Downstraam and Ambient Temperature 1000 ft. Upstream from Diffuser System on 28 November 1972. 84 14 Decay of Jet Centerline Velocity 87 15 Decay of Excess Temperature Along Jets 88 16 Variation of the Discharge with Excess Temperature of 5'T or More 90 17 Temperature Distributions Along the Mississippi River for Average-February Flow and Meteorological Conditions and 1974 Power Plant Capacity Factors; and Pen.issibic New Plants Based on Predicted Natural Temperatures 92 18 Temperature Distributions Along the Mississippi River for Average-May Flow and Meteorological Con-dicions and 1972 Power-Plant Cap-acity Factors; and Permissible New Plants Based on Predicated Natural Temperatures 93 0
111
~
4 i
.O l I
List of Tables. !
i i
Page, Table No.- Title (
I 1 Background Data for Single-Port Diffuser-System Studies ;
in 1973 and 1974 72 !
2 Results of Single-Port Studies .
on Prototype Diffuser System 73 3 Background River-Flow and Plant Effluent-Data 77 r
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Thermal and llydraulic Perforn.nce of the Quad Cities Nuclear Station h Waste-Ileat Dif fuser System 1
- 1. Introduction and Background. The Quad Cities Nuclear Station (QCNS) was designed and constructed during the second half of the 1960's and early 70's, and us .ompleted in 1971. At the time it was under design, no thermal-discharge standards had teen established for the Mississippi River, and, accordingly, a very simple system was designed and constructed to discharge heated water to the River from the condensers. The discharge structure was an open channel which intersected the shoreline about 750 ft downstream from the intake structure and was inclined about 30' to the perpendicular from the shoreline. It was anticipated that the submerged spur dike immediately down-stream from the discharge would be modified to direct the heated water toward the deepest part of the river channel, which is nearer the Iowa (west) bank.
The overriding criterion in the design of the discharge structure was to O
minimize heated-water recirculation from the discharge into the intake. This was a paramount consideration in the design of all power-plant discharge and intake systems in the 1960's.
At about the time the plant was completed, in 1971, river thermal standards were promulgated. One of the principal provisions of these standards was that an artificial heat load imposed on the Mississippi River could not produce a temperature rise greater than 5*F outside a mixing zone with area equal to that of a 600-foot-radius circle (or about 26 acres), for a River discharge equal to the seven-day-average River flow such that a smaller flow
- IPrepared by Drs. John F. Kennedy and Subhash C. Jain, Institute of Hydraulic Research, The University of Iowa. Iowa City, Iowa.
O 58
_ - - - . _ - . . . - . _ . ~ . . ~ . . - . - - . - . . - - -
l l
O occurs (on the average) once in ten years. This discharge is referred to as i the 7Q10 flow. The condenser flow from QCNS has a design discharge (flow rate) of 2,270 cfs (cubic feet per second) and a temperature rise (above the plant's intake-water temperature) of 23'F. Analysis of the river-discharge ,
records through water year 1969 for Clinton, Iowa, which is located about 15 miler upstream from QCNS, led to a 7Q10 value of 13,200 cfs at QCNS. Note that different values of 7Q20 are used in Kitanidis' analysis of River dis-charge and water temperature (Section II-A-1). The differences arise from use of ,
a longer period of record, through water year 1978, by Litanidis. A valuu of 7Q10 = 13,200 cf s is used in this Section, because that value was utilized in the design of the diffuser pipe, thermal analysia, and field-data program.
The fully mixed temperature rise curresponding to this 7QIO is ATQ10 " 23 N ) 11.2.5.IC18L. 3,93*y*
1a,230 (cfs)=
i This is the river-umperature r1se that would result if the QCNS thermal dis- [
charge were completely mixed with the 7Q10 flow. This value is so close to the maximu.a permissible value at the mixiag-zone boundary, 5'F, that it was clear that a s'.ructure would have to be devised which would achieve virtually complete mixing of the plant and River flows within a very short distance from the disd.arge structure. It was' also realized that the then constructed river-bank outf all likely would not meet the standards. Nevertheless.-because the shoreline structure already was in place, an intensive laboratory and theoretical study was undertaken to. detennine the temperature-rise distri-butions it produced 1.' the R'iver, and to investigate modifications to the structur- inich would imprcre its mixing characteristics. This study is O
59
described in a Universit, port (1)*. Suffice it here to say that no practical modifications structure were found which would enable the plant to meet the thermal standards under conditions of low River flows.
However, a simple means et 4str ,r t.cntly enhancing the mixing of the plant's discharge from the rive -b Apr r*.the n with the River flow was developed and subsequently used during eks s.,s cha dif fusar system was under design and construction. This modification consisted of a narrowing of the discharge-channel exit, by means of sheet-pile walls, to produce a jet with higher velocity and which therefore penetrated f arther into the River, and in the process became more diluted. This modified river-bank discharge structure is described by Jain et al (1).
The requirement that the plant's discharge be virtually completely mixed with the River within a very small area dictated the following require-ments for the discharge system:
- 1. Structural means be utilized to convey the heated water into the River. Figure 1 shows a map of the 1
area. The deepest part of the channel, indicated by the numbered (river miles) line with arrows, is seen to be closer to the Iowa shore. A jet dis-charge from the lilinois shore loses its momentum before reaching this part of the channel, where the River's flow is concentrated.
- 2. The release from 'che structure be staged across the River to be proportional to the product of local River
- Numbers in parentheses refer to items listed in the bibliography at the end of this report.
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depth and velocity (= local unit discharge), to achieve h nearly complete mixing of effluent and River flows.
- 3. The releases frcm the structure be virtually fully mixed with the River flow within a very short dis-tance from the release ports, to satisfy the mixing-zone and zone-of-passage requirements.
It was concluded that a multi-port diffuser-pipe system would be optimal for QCNS. The system designed and constructed is described in the next section.
II. Description of the QCNS Diffuser System. The QCNS diffuser system is depicted in Figures 2 and 3, and Figure 4 shows a cross-section of one cf the manifolds and risers. The two canifolds are 16-foot-diameter buried pipes, one about 2,100 ft long and the other about 1,700 ft long. Riser ports of 24 in and 36 in, diameter are spaced at intervals of 19 ft-8 in, and lh
- 39 ft-4 in., in an array that gives locally averaged unit discharge (i.e.,
port discharge divided by port spacing) f rom the manifolds that is nearly proportional to the unit River discharge (i.e., local River discharge per ,
unit of channel sidth). This distributes the heated-water release across the channel so as to be proportional to the local heat-assimilation capacity of the River, as determined from measurements and calculations of distributions of River velocity and depth across the channel, with the result that an almost laterally uniform River-temperature rise is produced. The risers extend vertically upward from the manifolds to above the River bed, and then are inclined 20' above the horizontal, as shown in Figures 3 and 4. Provision for later adjustment or " tuning" of the system was made in two ways. First, some flanged stubs were installed on the manifolds, to which risers can be O
62
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O 65
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l attached if it is found to be necessary to release additianal water at some 9i locations. Second, the discharge end of each riser was fitted with an orificed flange which is bolted to the riser. The diameter of each orifice is 0.9 of its riser diameter. The discharge distribution across the River can be modi-fied by replacing the flanges with others with different orifice diameters. The design and laboratory testing of the system were described by Jain et af (1),
Parr (2), and Parr and Sayre (3). Field testing of the system is reported by Parr (2) and Parr and Sayre (3). Representative results which demonstrate the thermal and hydraulic characteristics of the system are included herein.
III. Field Testing of the QCNS Diffuser System. The QCNS diffuser system was placed in operation in late 1972. During the period 2 November 1972 to 15 July 1976, 19 sets of detailed data on ghe distributions of temperature rise and velocity across River cross-sections were obtained at sections located various distances downstream from the diffuser pipes. Temperature-and velocity-distribution data were obtained also at a cross-section upstream from the pipes, to provide definition of the ambient flow and water-tempera-ture conditions. Subsequent to this period of intensive study, a set of data on cross-sectional distribution of temperature has been obtained during each calendar quarter, except for periods when high-flow or river-ice condi-tions made it dangerous or impossible to obtain flow and temperature data from a boat.
Field data on River temperatures and velocities were measured from a specially equipped boat that is outfitted with an instrumentation boom, special anchors, reflectors to permit positioning from a shore-stationed infra-red range meter, etc. Velocities were measured by means of a 10 cm Ott l
66 i
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o propeller-type current wate.c. and temperatures with thermistors and a special electronic system designed and built at the Institute of Hydraulic Research.
The velocity meter responds to velocities down to 3 cm per sec, and the tem-River discharges were perature-measuring system has resolution of 0.0l*C.
obtained from the U.S. Geological Survey for its gaging station at Clinton, lown (approximately 15 miles upstream), and f rom integration of measured velocities at the plant-site study sections. Data on plant load, condenser discharge, and condenser temperature were obtained from Commonwealth Edison Company.
Full details of the instrumentation, data-collection procedures, and results of the measurements obtained during the period of intensive study (November 1972-March 1974) are reported in Parr's doctoral thesis (2) sub-mitted to The University of Iowa, and in a University of lova report by Parr and Sayre (3). The results of the subsequent quarterly and sp.tcial measure-ments have been submitted to Cocraonwealth Edison Company by the Institute in letter reports. Typical results which demonstrate the hydraulic and thermal performance of the system over a wide range of cond'tions are presented here. ,
IV. Presentation of Results. There are three p . pal scales within which the thermal and hydraulic data on the dif fuser discharge should be examined: The near field, in which the temperature and velocity distribu-tions produced by individual jets are measured and analyzed, extends downstream to about the section where the jets start to merge or intersect the water surface. Near-field data are required for evaluation of the zone of passage, which is the fraction of the channel cross-sectional area or river discharge in which the temperature does not exceed a specified value. The next scale 67
of interest is the far-field, which extend, downstream from the end of the near-ficid to the sectirn where the heated jets become more or less fully mixed with the River flow. In the case of the QCNS diffuser system, the far field persists several hundred feet from the diffuser pipes. In the far field the mixing chara teristics of the whole ditfuser-pipe system are of interest. Finally, it is revealing tc exanine the gic.bal field, in which the heat transfer from tha river to the atmosphere becomes important. Study of the River from tY ;spective yields estimates of the rate of decay of artificially induced temperature rises, ano comparisons of induced and natural temperature variaticus. The global field extends dounstream for distances equal to several hundred river widths--typically several miles--to the section where the artificially induced temperature rise becomas insignificant. Also always of interest, of coerse, are the ambient conditions, end in particular the river-water temperature and its distribution across the channel at cross-sectior.s upstream from the section where the artificial heat load is imposed.
A. Upstream temperatures. Definition of the ambient or upstream temperature in a large river is by no means a straightforward task, because of l
the wide variations in temperature, not only vertically (due to gravity-induced thermal stratification during low river flow:), but owc , and often more importantly, laterally. Two examples of temperature distributions measured upstream from the diffuser system are presented. The background data for these e e included in Table 3, which is presented later. Figut. 5 shows temperature distributions measured on 3 December 1973, 200 ft upstream
'at two different times) and 500 f t downstream f rom the dif fuser pipes; and Figure 6 shows the upstream distributions before and after the downstream measurements on 15 July 1976. On both dates the maximum lateral temperature variations are seen to be about 1*C. The stratt.gy utilized in determination 68
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. .- - - .- -- .~_.. . - . . _ - _. . . -
of ambient temperatures from these somewhat variable upstream temperatures is ,
described in Section C.
Note in the River cross-sections shown in Figures 5 and 6 that the deeper-part of the channel, and therefore also the larger flow velocities and ,
unit discharges (discharge per unit of width), are near the Iowa shore, across-the River from QCNS, as discussed above.
B. Near-field surveys. Near-field temperature and velocity measurements were made just downstream from individual ports on seven dif ferent dates. These measurements were made primarily to obtain definition of the >
zone of passage, both with respect to area and with respect to discharge. For the present study, zone of passage is defined as the fraction of area of dis-charge, at a river cross-section, with a cemperature rise less than 5'F. The background data for and the results of these measurements are presented in Tables 1 and 2, respectively, and Figure 7 presents a typical set of field data. It is seen in Table 2 that at even the rclatively low River discharge of 30 October 1974, the zones of passage with respect to both area and dis-charge are above 75 percent, L Because of the time requirements for and great expense of field measurements, and because the River discharge cannot be controlled, it was not practical to obtain zone-of-passage data for all ports over a wide range of' River discharge. Instead, scale-model laboratory-flume experiments were l.
made by modelling longitudinal '_' slices" of the River. Some laboratory experi-ments included only a single port, while others itcluded three ports. Ex-l l-periments were made over the ranges of nondimensional parameters (velocity l- ratio. Uj/Ja, where Uj = jet velocity, Ua = ambient velocity; depth ratio, H/D.
O 71
T
' data for single-port diffuser-system studies in 1973 and 1974.
Table 1. 11ackgre Estimated Estimated Percent Velocity Discharge of Distance Local Plant from from Distance Full from Outlet Single Single Diameter Downstream Plsnt Ambient Effluent River Illinois Temp. Port Port from Port Loau Temp.
Date Discharge Shore o f I'o rt x P T, TE NJ J z D QR
(%) (*F) (*F) (cfs) (ft/sec)
(ft)
(cfs) (ft) (ft)
(7) (8) (9) (10) l (3) (4) (5) (6)
(1) (2) l 40.2 65.5 42.1 7.35 1 1774 2.7 35 88.5 11-16-73 39,600 65 37.2 61.4 46.7 8.16 1 82,210 1345 2.7 15 91.2 3 74 45
(
38.1 61.4 19.9 7.82 l
968 1.8 35 89.5 u 3-13-74 82,900
" 65 95 79.5 94.7 46.3 8.09 26,900 1313 2.7 15 50.0 l
7-24-74 45 75 57.2 96.0 27.3 4.77 2.7 15 78.0 10-01-74 28 600 1273 45 ,
75 53.5 104.5 24.0 4.19 1293 2.7 15 91.0 10 74 25,900 45 75 56.1 106.8 25.3 4.42 1391 2.7 15 87.8 10-30-74 25,200 45 75
- 9 e
, f\
"g.
J .
Table 2. '.Results of single-port studies on prototype diffuser system.
2nate Distance local- I scal Port Estimat ed Es t imat ed 2one-of Hasimum Zone-of -
lAmmst ream Average Average. " Spacing Effluent. Mimed Passage Observed Passage p from Port Ambient brpth Discharge Temperature wit - Temperature htt' ,
Velocity from Rise . Area Rise Dischstge Single ;
Port F 4
x . U, ' ll LL ,
Q)
AT ZFA (T-T,) ,,, ZPD.
(ft) (ft/sec) (ft)" -(ft) (cfe) (*F) (1) (*F)' (1)
(2) (3) '(4) (5) (6) (7) **? (9) (10) 11-16-73 35 1.52 23.4 19.67 42.1 1.44* 99.2 5.4 98.3 L 65 100 100 k e
15 2.88 21.7 19.67 46.7 0.898 97.3 7.7 96.5 l O . 3-12-74 99.6 45 99.7 5.6 ,
{; 6 i
ga 3-13-74 35 2.18 17.9 39.33 19.9 0. 30
- 100 4.4 100 L 100 100 -
65 I.7
] *$ '100 1.4 100 l Oy 95 2 n.
3I35-74 15 1.06 18.8 19.67 46.3 1.31# 100 4.9 100 i 45 500' 2.4 ' 100
-J 75 100 1.9 100 f
+
. La j 10-01-74 15 1.18 22.0 19.67 2s.3 2.11f 89.5 14.8 86.2 i
. 45 94.4 6.7 91.9
- 75 .100 4.0 100 f 10-25-74 15 1.07 20.0 49.67 24.0 2.64# 6.1 19.0 81.2 45 d6.7 8.9 81.5 i
]
3 75 .9?.5 6.0 97.0
,kIU23U14 7 15 1.09 20.4 19.67 25.3 2.7tf 87.1 20.0 76.2
- *% 45 87.2 8.7 85.3
! %% 75 98.6 5.7 98.5 i i 2l .
I-
- Calculated from A1 ,= y)AT El(LLIUa)+ -!
, # Computed f rom data measured at section 75 f t. ' downstream. t i
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ts nn 9t ,2 y n9 a *g 4
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. ,* 7 3
e
- 48 e s 5[g r 04 a8 68 o.7e6 9,6 S, u 0
6 J.
s3 a*s s
o *t s s# es 4: ?
os# 'o- g o,c o_ s ~
et i
. ~ - s_ l_ _ - - F s * * , ,
S I
g g y ,
, 2 2
y *i c# a dgm 4oyy 3o Uo. .
gc 8
4*
2 ; J ia; i
O where local H - flow depth, D = jet diameter; and density deficiency, (pa - Pj)/Pa.
wl re Pa = ambient-flow density, p) - jet density) that occur in the prototype.
De' .iled measurements of temperature and velocity were made in the laborer -, 7 f' ame downstream from the model ports. Corresponding laboratory and
.ata (discussed above) were compared and found to be in good agri _
zones of passage calculated from the laboratory data on valocity 4 ture at various downstream sections then were compared to determir.1 e b
mum zone of passage with respect to discharge for the whole Rive .-
the case in which both of *.he Station's units are operating at full _a and being cooled through the two diffuser pipes. This was do, b c '.c . .
the discharge in the sector (river slice) of each jet with tempercure ' . -
less than 5'F (including ef fects of jet interference or " overlap"), summing these discharges for all ports, and dividing by Qr. This process was repeated for several downstream sections, and the one giving the minimum zone of passage with respect to discharge was selected as critical, and used in the subsequent analysis. The result is shown in Figure 8, where it is seen that the areal zone of passage for full-load operttion of the plant is expected to exceed 75 percent for all River flows greater than about 15,300 cfs. In Table 2 it is seen that the zone of passage with respect to area exceeds that with respect to discharge (as was verified in the laboratory experiments), so the latter, given in Figure 8, is the limiting value.
Complete details of the laboratory experiments and procedures used in calculstion of rone of passage are given by Parr and Sayre (3) .
C. Far-field surveys. The background data for these surveys are For the far-field studies, the plant was being fully cooled g given in Table 3.
75
100 , ., , , , ,
3 P
90 - . -
4 i
So - .-
ZPRD -----
(%) l 70 -
l-I a .
l 60 - I -
l 1
1
~so 11 I i 'l I I I Io,000 "
20,0oo 30,000 44000 sopoo 1
l I' MISSISSIPPI RIVER DISCHARGE (IN CFS) 1 Figure 8. Minimum zone of passage with respect to total river discharge for the case of plant operation at full capacity. ;
I l O O .O I
.. . _ _ - . . _ . . . . =. . _
in the open-cycle mode through the two-pipe diffuser system. The plant was operating at nearly full' load during all surveys except the one made during low River flow, in July 1976.- Most of the measurements were made 500 ft downstream from the diffuser pipes, because a section 500 ft long extending across the full 2,200-foot vidth of the River contains approximately 26 acres.
Field and . . oratory data indicated that the jet diffusion and mixing of the l effluent with the River flow was practically completed upstream from this section. Figure 9 shows, as an example, the downstream temperature distri-
.butions measured on two different dates. The temperature-rise distributions then were calculated from the measured upstream and downstream temperatures, such as those presented in Figure 9, in the following way. The upstream temperat res measured before and after the downstream mcasurements at each vertical were both depth-averaged, and then time-interpolated to obtain a O background temperature at the time of measurement at each downstream-section l vertical. This depth-averaged, time-interpolated background tempt.rature at !
i the-lateral position across the River corresponding (as a fraction of River width) to a downstream measurement vertical then was subtracted from the point temperatures measured along that downstream. vertical. An example of a temperature-rise (or excess-temperature) distribution so determined is shown in Figure 10. This example is from the 1976 low-flow period; temperature-rise isotherms corresponding to Figure 10 are shown in Figure 11. On this Figure the regions within which the temperature rise exceeds 2.08'F (which would be 4
very nearly the areas within which the temperature would exceed 5'F for full-load operation of both units) are cross-hatched, and the corresponding area ratio is shown. The 5'F zones of passage for the flow of Figure 11 is about 88 percent.
78
, ..s 'J "'
I i i I l 't . g o ,_ _ rS CC 01- 16 -74 ,yY 9a W' C
- '. .N ,,7
') A
- .. 2.
- 3 ..
.= u.. .
o, o,
.. 2 , , . .
8 to- 's ., ** ** " ** *, **
u, .e s, ,, ,,
.o
,, "us .*'s -
- . ,, ,, s. es,e
& 20- , ** st o s. o j ~
u o
re -
%< JO -
4 3
0 u , 31 #r 1 TI.pov 0 12 73
- r .
- ,=
1 et g, .: .. .. .. .. a
., .. . . ..., , .. 3 q.
lO -
3 % :: ,, .. ., .. p 20 - *'
g
~ ( .. . , , ,
- n.
$ JO - -- , f .
._ ,{ - A - '
I , '
O SOO 1000 l$00 300 gggg Distance from Illinois shore in :t Figure 9. Obsesved point-temperature rises, in F, 500 ft downstream from the diffuser system, 3 December 1973 and 16 January 1974.
- 9 e
. . - - . . - . - - . . . . . .~. ,, - - . _ .. - - - . . - - .
v .
- 3 i
.i f01 ~24 i I i l o- Td O T, BEFORE,10:20 TO l1220 A.M.
2.2 -
g_
e' -. T, AFTER, 3:40 TO 4:40 P.M.
2.0 -
1 e /
w l.8 et e
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- n.
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.w l.6 - O
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yd 1.4 O
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e W -
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- O o O O
O , , , ,
1.0 O O.2 0.4 0.6 0,8- 1.0 ILLINOIS z/W IOWA Figure 13. Transverse distribution of depth-averaged temperature,
~
in C,'500 ft downstream and ambient temperature, in C, ft upstream from diffuser system, on 28 November 84
. .u - _._ _ _ _ - . . . . . _ . . . _ . . , _ . . _ _ . _ , , . _ , . . _ . . _ , , , . . _ . _ . _ . . . . _ , . _ , _ . . . . , . _ .
l diffuser system is failing to achieve fully mixed conditions. It is seen llh that the temperature dif ference between these two curves is no greater than the natural anbient-temperature variation across the River upstream f rom the diffuser.
Finally, it is pointed out that the performance of the dif fuser syttem could be improved, if this were deemed worthvile, through " tuning",
by adjusting the orifice sizes in the port flanges and installing additional risers to redistribute the effluent discharge across the River.
D. Summary. The diffuser-pipe system is yielding virtually com-plete mixing of the effluent with the River flow within a reach of the River that extends about 500 ft downstream from the diffuser pipe. A distance of 500 ft corresponds to about 25 river depths or one-fifth river width at this section, and the area included between this section and the diffuser system lh is about 26 acres. The practically instantaneous mixing of the ef fluent with the receiving water is a consequence of the well known dispersion procerses that occur in jets. A jet discharged into an otherwise quiescent or slowly moving body of water produces very strong velocity sherr-zones or velocity gradients around the jet boundary. This region of strong shearing motion produces very large vortices or eddies which burst outward from the jet boundary, envelop surrounding fluid, and entrain it inLJ the jet. The slower moving fluid which is entrained into the jet causes the jet to lose some of its velocity. The net result of this self-induced, rapid entrainment of surrounding fluid is for the jet fluid to become very rapidly mixed with its surroundings, while in the process dissipating :s own velocity and ac-celerating the fluid which it entrains.
O 85
O V. Further Detailed Analysis of Discharge through and from Diffuser-Pipe System. This section presents results of further, dt. tailed analysis of the jets discharged by the diffuser ports, which leads ultimately to a determination of the water-surface mixing zone (area with I > 5'F).
These results are based on a act.h . teal model developed by Parr and Sayre (3) to predict the performance of the diffuser system. The results of their i
mathematical model have been demonstrated to be in good agreement with pro-totype observations, as was discussed above.
Figures 14 and 15 show the decay with time of excess temperature and velocity, respectively, along the jet certerline for small and large ports. These figures are for a river flow of 13,200 cfs (7Q10), a condenser fov of 2,270 cfs, and an excest. temperatur., of 23*F (full-load plant opera-d tion). The results are based on the following two equations developed by Parr and Sayre (3) in their experimental and theoretical investigation of the QCNS diffuser-pipe system. These equations give the jet centerline excess temperature and velocity at a distance x downstream from the port:
Te - Ta " 0. 28 x._ + 0. 7 Tg - T a Dp and Ui - Ur = 0.23 x + 0.6 Up - Ua %
in which Te = effluent temperature; Ta = ambient temperature; Tg = jet center-line temperature; Uj = initial j et velocity; Ua = ambient flow velocity, and Ug = jet centerline velocity; x = distance downstream f rom the port; Dp = port diameter. The jet centerline temperature reaches the fully mixed 86
10 i i . . . .
9 g = 13,200 cfs _
r g8 -
- o. -
e7 _
D g
o 6 -
i
. 5 -
Large port
.E ~
E_
c 4 - _
e 83 -
~
Small port _
,. 2 -
l _
O O 10 20 30 40 50 60 Distance downstream from port (f t)
Figure 14. IMeay of jet centerlirie vnlocity.
- O e
c 1
O O- iOJ l t R
L
_ 25 .. . .
. i i ta.
L-W E ~
O O = 13,200 cis f
4 \ ~
E w \.
G-15 l -
1 w \.
> \4 h '
LARGE PORT- >
W 10 -
\. \
8 d s . FULLY MIXED T EMPER ATURE-td '
N .'N RISE N
- SMALL PORT}.
c 5 . ~ . .
_ , _ , ^ - -
m ---
4 H
<3 ' ' ' ' ' ' ' ' '
0 ' '
O I 2 3 4 5 .6 7- 8 9 10 11. I? 13 14 15 !
TIME OF. PASSAGE (se'c) >
- -[
Flytare 15. Decay'of excess tem [w**ture along jets.
i t
-l
temperature in a very short time, as can be seen from Figure 14. At higher river flows this time would be even smaller. The jet centerline velocity decays in a short distance (Figure 15): The effect of the river velocity on the decay rate of the jet-centerline velocity is not large.
The variation of the discharge with excess temperature of 5*F or more, Q5, as a function of distance x from the port exit is shown in Figure 16.
The value of QS at x = 0 is equal to the condenser water discharge (2,270 cfs).
As one would expect, Q; first increases, reaches a maximum, and then decreases to zero. The maximum value of QS for a River flow of 13,200 cfs is about 3,700 cfs, which is about 28 percent of 7Q10. The maximum value of QS in terms of percent of river flow decreases with increasing river flow.
An analysis conducted to determine the river-water surface area covared by the 5*F isotherm of excess temperature for a ccadenser flow of 2,270 cfs at 23*F excese temperature revealed that this surface area is zero, if gj/qa < 3.8 for the large ports, and q3 /qa < 6.0 for the small ports (qj and qa are the jet and local river discharges per unit vidth, respec-tively). The measured velocity distribution in the River at low River flow indicates that most of the ports satisfy these conditions; a conservatively high estimate is that five small ports and ten large ports will not meet these conditions. Further computations for a River flow of 11,200 cfs showed that the length of the upstream thermal vedge and of the downstream plume where the excess temperatures exceed 5*F are 20 ft and 100 ft, respectively, for the small ports; and 20 f: and ' ft, respectively, for the large ports.
For thest values, the surface area included within the 5*F excess-temperature isotherm was found to be less than two acres.
9 89
( [
' V) i i i i
- i i 4000 -
O, = 13,200 cf s TOTAL
". , *,,,---LAPGE - s~~~.~~
PORTSd N'~,
3000 -
,s*
y 1 ,a #
- ,o M #
O ,
2000' e
o 1000 -
SMALL PORTS O 20 25 30 35 40 O 5 10 15 DISTANCE DOWNSTREA;A FROM PORTS (f t)
Figure 16. Variation of the discharge with excess temperature of 5 F or more.
1
(
h r s --w _,
m VI. Global-Field Perspective. A natural body of water is in thermal equilibrium with its surroundings, in the sense that, over a suffi-ciently long period of time, it gives up as much heat as it receives. The prir.cipal natural source of heat is solar radiation. Heat is lost from the body of water through the processes of evaporation, convection, conduction, and radiation. The rate of heat loss due to each of these processes increases as the water temperature increases. In this way the temperature increase produced by an artificial heat load imposed on a body of water, as in the case of the QCNS heated discharge, leads to rates of 1. cat loss from the water body that are higher than the natural vlaue, and cause the water temperature to return to its equilibrium value. Thus the heat injected into the water eventually is transferred to and through the atmosphere by the aforementioned processes, and the river-water temperature approaches its natural value as the flow proceeds downstraam. It is illuminating to examine the variation of natural temperatures along a river, and also the rates at which induced-temperaturr. rises are dissinated along the flow.
Studies recently completed by the Iowa Institute of Hydraulic Research for the Mid-Continent Area Power Pool (4) and the U.S. Department of Interior (5) develeped a computer-based model for calculation of river tem-peratures, and applied it to the calculation of the thermal regimes of the Mississippi and Missourf Rivers. The numerical model utilizes historical hydrological, meteorological, and channel-geometry data, as well as data on the magnitudes of artificial heat loads imposed on the River. Figures 17 and 18 show temperature distributions along the Upper Mississippi River for l average February and May flow and meteorological conditions, respectively, l for several different thermal loadings. The heated discharge from QCNS 91
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very low flows. Diatoms remained dominant during these lower flow periods; i however, the populations were less abundant than usual and not as diverse.
Peak densities occurred in spring (April and May) and in fall (October and i November). Seasonal lows occurred in winter (January and February).
The slough habitats generally. supported the largest and most diverse phytoplankton populations. These relatively quieter areas are generally.recog-nized to be biologically 1mportant areas of high production. As water levels )
increase,_the backwater hr.bitats and slough areas-are inundated and, as flow
- O l 100
s ,% - u_ .- - , . .a.4--#A.a__ u-au .a.. J A.- ae-a _., . .4__ - --- . - --_.. A O,
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declines, the drainage contributes to temporarily increased densities of O plankton in the river. There were few differences in the density or composi-tion of plankton assemblages between the main channel and main channel border locations. Differences in phytoplankton assemblages between the Wapsipinicon j and Mississippi Rivers were, however, evident.
No consistent significant changes in species composition or distribu- l tion of organisms in this group were observed between control and potentially impacted sampling locations in the river. Most importantly, phytoplankton densities and comunity compositions were not measurably different between the areas upstream and downstream of the diffuser pipe during open cycle operation.
Effects of condenser passage on phytoplankton were evident for operation with both the side-jet and diffuser. The effects on entrained phytoplankton were, however, inconsistent. Slight increases in phytoplankton productivity and ,
chlorophyll a_ concentrations were periodically observed at locations immedi-
.ately downstream of the diffuser r;.ipe. However, these slight increases were not measureable outside the immediate discharge area. l t
- 3. Zooplankton Studies The summary is based on Hazleton Environmental Sciences (1979a, pp.
~4.1 to 4.29). Zooplankton reach their maximum seasonal abundance between April and June with relatively smaller pulses c: curring in the summer and late fall.
Rotifers and immature copepods usually account-for the majority of the zooplankton. Differences in zooplankton abundance were noted between the.
various slough, main channel and main channel border locations. In addition, assemblages in_the Wapsipinicon River were noticeably different than the
' 101
Mississippi River an.semblages. There were no appreciable changes in the natural seasonal patterns of the zooplankton populations of Pool 14 through-out the menitoring program.
Consistent significant alterations in species compositiot. or distribution of zooplankton were not observed between control and potentially impacted sampling locations in the river. In particular, zooplankton densities and cocnnunity compositions were not appreciably different between areas upstream and downstream of the diffuser pipe during open cycle operation. The program designed for apsessing the effects of Station oper. tion on this group of organisms would have detected any major change in th.s community since differences between seasons, locations and years and the two rivers sampled were observed.
- 4. Periphytic Algal Studien This summary is based on Hazleton Environmental Sciences (1979a pp. 5.1 to 5.68). Diatoms ware the most commonly encountered periphyton with species of 1:avicula, Gomphonema,1;itzschia and Melosira generally the most cot:: mon f orms. Dominance by green and blue-green algae occasionally occurred during the summer. Seasonal trends of periphyton density were generally comparable throughout the mon!,toring program with peaks occurring from mid-summer through early fall. Losest production occurred during December through March. This seasonal succession within the periphyton consnunity was undoubtably af f ected by changes in chemical and physical factors such as water temperature and nutrient concentrations.
102
Blue-green and green algae vere more abundant in 1976 than during O
- the other years of monitoring. As with phytoplankton, diatoms remained dominant during this low flow period. The slightly different physiochemical factors associated with the extraordinarily low river flow in the year, were probably responcible for the prevalence of these algal components.
Periphyton abundance, as measured by total biovolume and biomass and chlorophyll a_ production values, was variable among sampling locations, both
~
between and within years. The differences between these three measures are attributed primarily to seasonal changes in both photoperiod and chemical and physical factors. Differences in abundance and composition between the Wapsipinicon and liississippi Rivers were especially pronounced and were attributed to differing water temperatures, currest velocities, turbidity and nutrient levels. ,
O Periphytic algae biomass values and chlorophyll a concentrations were reduced in the discharge bay and in the immediate discharge area during side-jet operation. These differences were expected and attributed to Station operation. No differences were found in the river, however, during diffuser pipe operation. The lack of differences was attributed to the translocation of the plume to the main chennel and to the rapid mixing of the discharge with river water. This is especially significant in view of the effects observed during closed-cycle condenser cooling which results in the occurrence of a thermal plume escaping f rom the intake bay. This plume occupies an extrmely small f raction of the river's cross sectional area along the Illinois shoreline. Some very localized and minimal effects on periphyton production and composition patterns were attributed to this intake plume, 103
No consistent significant alterations in species composition or distribution of organisms in this group were observed between control and potentially impacted sampling locations in the river due to operation of the Station. Furthermore, it is unlikely that any significant differences could occur since the warm water discharge for open-cycle operation is to the main channel outside any area where periphyton attachment would naturally occur.
- 5. Benthic Macroinvertebrate studies This su= mary is based on Hazleton Environmental Sciences (1979a pp. 6.1 to 6.148). Benthic macroinvertebrate monitoring of Pool 14 has been accomplished through the sampling of natural and artificial substrates and drift sampling. The various sampling techniques have collectively provided for a complementary monitoring of all of the various lif e history stages and habitat preference of the macroinvertebrates of this area of the Mississippi River.
The composition of the benthos community is highly dependent on .
the river flow, sediment type and season at the time of sampling. The dominant organisms collected were the aquatic worms (Naididae and Tubificidae), burrowing mayflies (Hexagenia spp.), net-spinning caddisflies (Hydropsychidae) and midge flies (Chironomidae).
The most consistent spatial difference in abundance and composition was between the main channel and main channel border habitats. The main channel which receives the highest temperature rise for open cycle operation is characterized by a shif ting sandy battom and has lower abundance and less diversity. Ir addition, the thermal plume from the diffuser system is O
104
~ _ _ _ _ _ _ _ _ . _ _ _.
I I
bouyant which results in little, if any, temperature increase in the area.
Main channel border locations on the other hand, are usually characterized by a higher proportion of silt and clay in the rabstrate and have more tubificids, chironomids and Hexagenia. In addition, the more widespread occurrence of Hexagenia was commonly noted during extended low flow periods, possibly due to increased s11tation.
yreshwater mussel (Pelecypoda) populations differed between upstream I
and downstream locations in the main channel border habitat in the vicinity of the Station. Species occurrence rad densities of mussels were greater at the downstream locations than at the upstream locations. These differences
-vere apparently related to the more favorable hydrologic conditions at the I
downstream locations which were characterized by having a continuous current l and a silty gravel substrate. Since t,hese locations are not impacted by the plume from the diffuser system, no association of these differences with ]
Station operation would be expected.
l Naididae (aquatic worms), Hvalella azteca (amphipods) Hepta-ga.nidae I
)
(mayflies), Hydropsychidae and Psychomyiidae (net spinning caddisflies) and !
Chironomidae-(midge flies) were the predominant organisms callected on artificial substrates.. Community composition and density on the artificial habitats
-fluctuated at all sampling locations presumably due to changes in annual river flow and season as well as local sediment character and current velocities.
l- Recruitment or drif t of- organisms f rom the Wapsipinicon River also af fected
_ populations _. downstream from the river's confluence with Pool 14. ,
There were no measurable effects of Station operation on the-benthic macroinvertebrate coccunity downstream from the Station resulting from open--
O 105 j i
j
cycle (diffuser) operation. Dredging operations during the installation of th diffuser pipe system in 1972, resulted in a temporary downstream change in sediments and community composition but both sediment characteris-tics and community structure returned to normal a'ter dredging was cen:pleted.
The ability to detect and follow the progression of change associated with dredging demonstrates the sensitivity cf the monitoring program.
Entrained macroinvertebrates nuffered mortalities in the discharge bay at high water temperatures. No significant detrimental effects were observed, however, in the Mississippi River when drifting macroinvertebrates passed across the mixing zone of the diffuser pipe system.
Benthic macroinvertebrates on both natural and artificial substrates were affected by the thermal plume escapement from the intake bay during closed cycle operation. These effects were restricted to a limited area outside the intake and along the Illinois shoreline.
Operation of the diffuser pipe during combination cycle also appeared to have no measurable effect on benthic macroinvertebrates on natural substrates downstream of the Station. As indicated earlier, this finding was expected because of where the diffuser discharges (main channel) and the bouyant nature of the thermal plume. Populations colonizing artificial substrates, however, appeared to be altered by increased densities of Nais bretscheri (naidid) and Glyptotendipes (midge). These increased numbers were attributed to drift of these organisms ou: of the spray canal through the diffuser pipes since similar increases were not found during 106 9
l
() open-cycle operation. Qualitative sampling conducted in 1977 showed these two species to be very comnon in the spray canal. This finding is considered to be an artifact since the artificial substrates were located in the water column off the bottom and is probably not applicable to natural substrates in the area of the discharge. Once again, no consistent significant alterations in species composition or distributions of organisms in this group were observed between control and potentially impacted sampling locations in the river associated with diffuser operation.
- 6. Ichthyoplankton Studies This summary is based on Hazleton Environmental Sciences (1979a pp. 8.1 to 8.74) and Hazleton Environmental Sciences (1979b). Larval fish populations in Pool 14 of the Mississippi River near Quad Cities Station
() have been monitored since 1971 through the use of towed net samples. Comparisons of data from 1971 through 1974 were difficult to make because sampling frequencies, techniques and locations were inconsistent among years. Since the sampling design was more consistent from 1975 through 1979, data com-parisons were made for these years only for this Demonstration.
Treshwater drum eggs have been the predominant fish eggs collected j during each of the five years and have proportionally increased cach year f rom 66% of the total eggs collected in 1975, to 98% in 1978, and 97% in 1979. Freshwater drum egg densities peaked when ambient river temperatures were about 68 to 71.6*F during each of the five years. Usually these temperatures (and high densities) occurred during late >by to early June.
The taxa of fish larvae collected have remained constant with fresh-() water drum, carp and cyprinids (minnows other than carp) being the most 107
abundant taxa during the five years of study. Other abundant taxa included catostomids (suckers), white bass and gizzard shad. Ichthyoplankters typically appeared in the drift in mid to late April each year, with the greatest numbers occurring in mid-June. Few remained in the drift after July. Ambient river water temperatures appeared to directly influence the density of ichthyoplankton.
Most of the total ichthyoplankton drift occurred when ambient river water temperatures ranged from 64.4 to 71.6'F. However, there was no obvious correlation with river flow. The onlj exception to this was in 1977, when it appeared that low river flow influenced spawning success. As a result, most ichthyoplankton were collected later than during other years.
In 1978, an intensive sampling program vaa conducted during the period of peak larval abundance with special emphasis on the freshwater drum (Eazleton Environmental Sciences, 1979b). This study demonstrated that there was little difference between average day and night abundances. There were also no great differences in vertical distribution of all larval stages combined. There were, however, consistent horizontal differences with the main channel and Illinois side of the river exhibiting somewhat higher total larval abundance.
The above conclusions were based on analyses in which all larval stages were combined. In 1978, diel, vertical and horizontal density differences by larval stage (yolk-sac, post yolk-sac and juvenile) were also investigated (Hazleton Environmental Sciences, 1979b). In general, the various stages were distributed similarly to the total except for yolk-sac larvae which at night exhibited much higher abundances in the bottom samples.
108
During 1978 and 1979, samples were collected at a location immediately below Clinton Lock and Dam, anothet m ion between the Station and Clinton Lock snd Dam, and a location in the Marais D' osier Slough (Cocoonwealth Edison Company, 1980). The location farthest upstream (Clinton Lock and Dam) was used to measure contributions of freahvater drum eggs and larvae to Pool 14 from Pool 13. The other two locations were needed to determine whether the usual sampling area (immediately above the Station) was unique with respect to being a freshwater drum spawning and nursery area. Freshwater drum eggs and larvae were abundant at all locations in both years demonstrating that Pool 13 and all or Pool 14 above the Station are spawning and nursery areas.
- 7. Adult and Juvenile Fish Studies This summary is based on Mazleton Environmental Sciences (1979a pp. 7.1 to 7.145) and Commonwealth Edison Company (1980, pp. 3-1 to 3-52).
O Adult and juvenile fish monitoring has been conducted in the area of the Quad Cities Station sir. e 1971. The program was modified several times in the interval 1971 through 1977, to address specific objectives rej sted to Station operation. In 1978, results-of the previous years' studies were reviewed, and those' sampling techniques (electroshocking and bottom trawling) and sample locations which had the greatent continuity since 1971, were selected for incorporation in a long-term monitoring program that is currently underway. In 1978, an additional method of sampling, haul seining, was incorporated into.the long-term program to provide relative abundance and standing stock estimates'for several species not adequately sampled in previous studies. This was done at the suggestion of the Iowa Conservation Commission. Finally, at'the suggestion of the Illinois Department of Conservation, fall fish standing stock estimates for slough habitats based 109 1
i on a cove rotenone technique of sampling, were initiated in 1979.
O1 1 Electroshocking rifty taxa of fish have been collected by electroshocking during the cdne years of investigation (1971 through 1979). Of these 18 or 36% were captured every year. The number of species collected in a particular year has not varied significantly and has ranged between 27 (1975 and 1977) and 33 (1973). Differences in species occurrence during these years resulted primarily from the sporadic occurrence of taxa which are uncommon or are generally not vulnerable to electroshocking. Eight taxa were collected at least once between 1971 and 1974, but were not captured thereafter; these were yellow bullhead, taJpole madtom, brook silverside, yellow bass, green sunfish, yellow perch and log perch. Paddlefish, goldeye and blue sucker were captured only s,)oradically after 1973. The five most abundant species collected over the nine years of study were gizzard shad, carp, bluegill, river carp-sucker and freshwater drum. P terms of the more abundant species, there has not been any continuously progressive increase or decrease in ranking.
Total catch-per-efforts (CpE's) from earlier years vera calculated both with and without gizzard shad because sampling efficiency for this species varied. Collection efficiency of stunned gizzard shad prior to 1976, was insufficient to adequately represent true abundances of this species and electroshocking results underestimated their relative importence in the study area. An extra effort was made from 1976 through 1979, to collect all shocked gizzard shad. To allow better comparability between years, relative abundances discussed here are "without gizzard shad." Numbers, O
110
7 CPE and relative abundance (%) of fishes collected by electroshocking for O 1971 through 1979, are given by location and habitat in Commonwealth Edison Company (1980 Appendix C, Tables C-4 through C-30).
The annual total CPE values (without gizzard shad) for the entire study area were similar among the one year of preoperational monitoring (1971) and the first two years of operational monitoring (1972 and 1973).
During these first two years of operation, the Station operated open-cycle.
From 1974 through 1979, when the Station principally operated closed-cycle (spray canal only) or partial open-cycle (single dif fuser plus spray canal),
there was a substantial reduction in cooling water utilization, but an overall decrease in annual CPE was observed. A succes.sive decline in CPE was observed in 1974 and 1975, remained low in 1976, decreased in 1977 and 1978, and increased slightly in 1979 (Commonwealth Edison Company,1980, Figure 3-5).
This pattern of decline in annual CPE values for the entire study area from 1971 through 1979, was also observed within each habitat type.
In 1972, the total CPE increased slightly at the slough location and continued to rise in 1973. 11owever, during the next four years (1974-1978) there was an overall decrease except during 1976, when this habitat van not sampled.
CPE values for main channel border and side channel border generally were similar and, although lower than values recorded for the slough habitat, followed the same trend described earlier for the nine year period.
Some differences in CPE values were detected between comparabic habitat locations upstream and downstream of the Station. Regardless, the yearly Q 111
pattern at these locations was similar with highest CPE's in 1971, 1972 and 1973, followed by a steady decline over the next fi e years except far slight increases in 1977 and 1979. These data indicate that factors affecting the fish community from 1971 through 1979, were similar within ea:h habitat throughout the study area. Since the decrease was observed at both upstream (control) and downstream (potentially impacted) locations, it cannot be attributed to the thermal discharge associated with Station operation.
It is possible since catch-per-unit-effort was higher during the earlict open-cycle years than during the later closed-cycle years, that Station operation affected subsequent population levels because of entrahment and impingement losses. It is believed, however, that this is not the case as is discussed in the entrainment and impingement sections of the 316(b) Demonstration S"pplement (this volume). Entrainment losses are expected to be about the same for larvae during open or closed-cycle operation. Impingement is also unlikely,to result in population decreases of the magnitude seen over the study period because very low percentages of the total Pool 14 nopulation are lost. Impingement losses can be considered to be inconsequential in terms of maintaining population levels. In addition, fluctuations in fish communities are common prenc,nmena and may be caused by a variety of f actors.
Bottom Trawling ,
A total of 34 fish species have been captured by bottom trawling from 19/1 through 1979. Of these, carp, silver chub, channel catfish and f reshwatt drum have been collected each year. Very little annual change in species com-position of the fish community has occurred during the nine year monMoring O
112
_ . . _ . . . .__ -..._._.._._._._.._____.__._._m._ -
)
1
)
.- program.--The five most abundant species in decreasing order of abundance have L -
befn channel catfish, freshwater drum, shovelnose sturgeon, silver chub and
-carp. One western sand darter was collected in 1977. The St+te of Iowa (Roosa, 1977) considere this species to be threatened.
Bottom trawling dats. in conjunction with temperature were used to evaluate avoidance or attraction of fish to the vicinity of the diffuser system. Asido f ror. decreaseo abundanc.es at the dif fuser location in 1972 (during installation of the system) there has been no corre ution between temperatre and fish catches in the diffuser area.
Haul Seine I
in 1978, an additional sampling method was introduced into the long term monitoring program. Haul saine locations were establiwhed upstream of the l 1
-Sts. tion in three habite.ts (side channel, slough and altered slough) to provide relative abundance estimates for several species which were not adequately sampled by trawling and shocking in previous studies. The haul seine was also introduced to provide a standing stock estimats for the side channel and alough habitats.
During the two years of monitoring, 24 species have been collected with species composition similar between 1978 and 1979 (Commonwealth Edison Company,1980, Tables 3-6 and 3-8) . Species abundance during 1979 was slightly ic.wer than in 19f8. . During both years, freshwater drum was the most abundant species captured generally f ollovel by ginard shad, n.ooneye, white bass, river carpsucker, quillback, white crappie, smallmouth buffalo and sauger.
- 113
_. _ . _ _ _ _ _ _ _ _ _ _ - _ _ _ . _ _ _ _. ~. _ . _ .-. _ _ _ . _ _. _ _
Results of the 1978 and 1979 haul seine collections were also used to estimate standing crop by species, number and weight for each of the three habitats surveyed. The estimated total standing stock for side channel and slough habitat was 88.0 and 260.0 lbs/acrt in 1976, and 42.7 and 288.6 lbs/ acte in 1979 (Commonwealth Edison Company, 1980, p. 3-43). The standing stock estimate for the altered slough habitat in 1979 was 18.6 lbs/ acre. (This area has been altered by a sand and gravel dredging operation.) Haul seine standing crop estimates are certain to be low by a substantial but unknown margin. This is due in part to escapement of small fish through the 1-1/2" bar mesh of the haul seine. Some fish may also escape through gaps between the lead line and substrate.
Rotenone Survey In 1979, the standing crop in the fall was estimated from a rotenone survey conducted in a cove in Marais D' osier Slough upstream of the Statios..
The area was blocked off with a net and electroshocked prior to application of the rotenone. Fish captured were marked and returned to the sample area. A total of 24 species was collected by rotenoning. Numerically, gizzard shad, vnite crapple and carp comprised 92% of the fish collected (84%, 6% and C 3%, respectively). By weight, gizzard shad, carp, northern pike and white crappie contributed 93% of the catch (50%, 32%, 8% and 3%, respectively)
(Commonwealth Edison Company, 1980, p. 3-37). Based on the results of the marking and subsequent rotenone sampling, the estimated standing crop of the surveyed slough was 5,398 fish /A with a biomass of 648.6 lbs/A.
O 114 I
.. . ._- . . . . . - - - _ - . _ . - . _ - . . . . _ . - - . - . - . . ~ . . - . . . . - . _ . . . - _ - - . _ .
t O In a previous study by Muench (1978) in 1977, one cove rotenone survey was conducted in an area near the site of the 1979 survey. Procedures were essentially the same As the 1979 survey, and results were similar for both species composition and abundance, standtng crop estimates of 566.0 lbs/A for 1977, and 648.6 lbs/A for 1979 are not considered to be significantly different.-
i e
O L0 .
F 115
O Literature Cited Commonwealth Edison Company, 1980. Quad cities Aquatic Program, 1979 Annual Report. Chapters 1 through 5 and Appendicles A, B, C, D and E.
Hazleton Environmental Sciences, 1979a. Environmental Monitorin3 in the Mississippi River near Quad Cities Station, August, 1968 through December, 1978. Chapters 1 through 8 and Appendicies A, S C and D.
, 1979b. Intensive Ichthyoplankton Studies ac Quad Cities Station, June, 1978. HES No. $50105739. 339 pp.
Heuoch, B.A., 1978. Standing Crop Estimate for a Pool 14 Y.ississippi River Eackwater Area. Paper preschted at the 16th Annual Meeting of the Illinois Chapter, American Fishery Society. February 21-23, 1978.
Roosa, D.M., 1977. Endangered and Threatened Fish of Iowa. Special Report of the Preserves Board No. 1. Des Moines, Iowa. 25 pp.
O O
116
O C. Effects of increased Temperatures on Fish by Dr. Robert G. Otto R. G. Otto & Associates Baltimore, Maryland October 27, 1980
9 Table of Contents Title Pm List of Tables 11 List of Figures 111 Introduction 117 Effects of Temperature on Fish - General Summary 118 Potential for Exposure of Fish to increased Temperatures at Quad Cities Station 120 Fish Species of Concern 121 Maximum Acceptable Temperatures for Prolonged Exposures 122 Maximum Acceptable Temperatures for Short-Term Exposures 134 Conclusions 138 Literature Cited 140 O
i l
1
I O
List of Tables Table No. Title M 1 Planktonic life stages of fish counnonly occurring in main channel habitats in Pool 14 of the Mississippi River. 123 2 tbjor components of the main channel fish assemblage in Pool 14 of the Mississippi River. 124 3 Preferred temperatures, maximum weekly average temperatures for growth and ultimate upper lethal temperatures for fishes occurring in Pool 14 of the Mississippi River. 132 4 Maximum acceptable exposure times (mid-su=mer) f or juvenile and adult fish entrained at the Quad Cities diffusers. 139 O
l 11
O List of rigures n gure tio. Title P8E' 1 The decay of excess temperature from a singic port of the Quad Cities diffuser. 119 9
e 111
__ _ .- _--~ - - - - - - - - . - - - -
Introduction O
This chapter deals with the effects that elevated temperatures resulting from once-through or open-cycle operation of the Quad Cities Station might have on the fishes of Pool 14. The physical and hydrological nature of Pool 14 and the changes anticipated as a consequence of open-cycle operation of the Station have been discussed in detail by Drs. Kennedy, Jain and Kitanidis (this volume). Briefly, the main body of the pool has an annual temperature cycle that ranges from a mid-winter low of approximately 32'F to a mid-summer high of about 78'F. The Station discharges heated water from a paired diffuser system located on the bottom of the main channel and-extending f rom the Illinois side of the river. The heated water is discharged from a series of ports or jete designed to promote rapid-mixing with ambient temperacure river water.
O The heated plume downstream of the diffuser has three principal components. The near-field (in which the mixing of heated and ambient waters ,
is driven by the process of jet entrainment) initiates at the individual .
ports and decays to form the far-field (in which any further mixing is driven by L:tural processes). The third component is the global-field, a region in which heated and ambient waters are completely mixed. It is from the 1atter two regions that most of the heat rejected by the Station is dissipated to the atmosphere.
Diffuser port exit velocities range from 8.5 to 9.3 ft/see when the Station is operating all of its six circulating water pumps. The AT or temperature rise above ambient is 23'F when the Station is achieving its O 117
. . .____.______._..:__._.__..._,_.,_...___..~. _ _ _ _.._ _,- _ ._,
maximum power output. The initial (near-field) time-temperature decay curve associated with entrainment mixing is shown in Figure 1. There is a proportienal decay of temperature and velocity while the volume of heated water increases accordingly. Principal factors affecting the shape of the initial decay curve are exit velocity, discharge temperature, ambient temperature and river velocity. Each of these can vary within limits as discussed by Dr. Kennedy. However, as a general case, the near-field is defined at each port by a velocity decline from 8-9 ft/see to about 2 ft/sec, a temperature decline from 23'F to about 4*F and an increase in plume volume due to jet entrainment of ambient water of about 6X.
The dimensions of the far-sield and global-field are highly dependent on seasonal conditions that ci rol the rate of heat loss to the atmosphere as well as on total river flow and ambient temperature. Under conditions of maximum power output and minimum river flows (7Q10), the entire main channel of the river downstream of the diffuser may be heated by as much as 3.95'F (Kennedy, thir volume).
Effects of Temperature on Fish - General Summary Temperature is the most extensively studied of the environnental variables that affect fish distributions and well-being (with the exception of geography). Recent and excellent reviews of the scientific literature have been prepared by Fry (1971 - Ecological relations) and Hochachka and Somero (1971 - Biochemical relations).
Discrete upper and lower boundary temperaturec exist for all life functions. Temperatures that set limits for survival comprise the O
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widest boundaries with successively narrower limits for avoidance, attraction, growth, swieting performance and reproduction. The specific limiting values for each of these functions vary with species. In addition, there is a certain amount of plasticity (resistance, acclimation or acclimatization) a'sociated with the life c.tage and previous enermal experience of the individual fish. The sit. gee exception appears to be reproductive function, for which thermal limics are fixed at the species or population level (Hokanson 1977). Any reproductive compensation for annual variation in temperature cycles seems to be restricted to alteration of the timing of the reproductive sequence.
Potential for Exposure of Fish t: Increased Temper _atures at Quad Cities Station The physical and hyi eological events described briefly above govern the circumstaates of exposure of Pool 14 rishes to elevated temperatures.
There are three principal cases of interest. The first two relate to the near-field and provide opporteuity for exposure to elevated temp.tratures approxima . .ng (but never equaling) the station AT. Tirnt, 'shes, and into planktonic eggs or weakly swimming larvae in particular, ray be swept the plume by the process of jet entrainment. Eccond, strongly swimming fish may of their own volition actually penetrate the plume in an upstr aam direction, drawn by an attraction to the elevated temperature or velocity but limited in the extent of their penetration by an avoidance response to high temperatures , swimming capabilities and the relatively small volumes available. The third circumstance occurs when the far-field and global-field comprise a substantial portior of the river downstream of the diffusers. Fish resident to main channel habitacs must then contend O
1 120
i e
O
~
with the events of day-to-day life in an environment that is slightly warmer (maximum of 3.95'F) than is normal for Po11 14.
~?here are also two secondary considerations relevant to fish exposure to'the thermal plume. The first, the potential for cold death or shock following shut-down of the Station (termination of the heate6 plume) is pertinent to a situation in which fish reside in and acclimate to the heated effluent luring the winter months. The second, gas bubble disease, is also a potential mid-winter problem for plume resident fish and relates to exposure to waters supersaturated with dissolved gases.
Fish Species of Concern l
The Mississippi River has an ancient and extreordinarily diverse
() _ native fish fauna, which has subsequently been expanded by the introduction of exottes More than 75 species representing 19 families have been f collected fro. Pool 14 during the ten years that the Quad Cities Monitoring Program has been in progress. The distribution of these species within the
' Pool is complex, reflecting the availabilf,ty of a variety of different habitat i
types as well as the seasonally chang 1ng ecological requirements of particular-species or age groups.
L The principal habitat types are the main channel, side channels, main channel borders, sloughs and tributary streams of various sizes. Since
-the Station diacharger to the open river (main channel) habitat, fishes in-habiting thtt region and, to a lesser extent, the shallower areas peripheral j to the main channel have the greatest probability of exposure to the heated effluent.
121 i- - _
The open-river fish assemblage has two principal components: planktonic or semibuoyant forms (eggs and early larvae), which are immotile or only weakly motile and drift with the current, and nektonic or free-swimming fishes (juveniles and adults) capable of controlling their own distributions.
The most common planktenic life forms include one species of egg (freshutter drum) and seven taxa of larvae (Table 1). The more common nektonic forms include 20 species (Table 2). The principal method of collection is also indicated in Table 2 as a means of discriminating species that are most often found on or near the bottom in open water (trawl) from those more commonly found in shallow water along shore (electroshocking).
Maximum Acceptable Temperatures for prolonged Exposures The design of the diffuser system places stringent limits on the opportunities of fishes for prolonged exposure to elevated temperatures.
e Since the majority of the near-field regions are unavailable to fish for other than brief periods, concerns for prolonged exposure are limited primarily to the far-field and global-field, regions no more than 4*F varmer than ambient waters.
The areal extent of the far- and global-fields varies widely depending on river flow and ambient air and water temperatures, parameters reflective primarily of seasonal climatic conditions. In addition, fish response to temperature or temperature fluctuations varies in relation to seasonal cycles, and we have chosen to structure our consideration of the effects accordingly.
Wirlev Winter is a period of low to intermediate flow and minimum ambient air and water temperatures. The rapid loss of excess heat to the O
l 122
j~'
L).
Table 1. Planktonic life stages of fish commonly occurring in main channel habitats in Pool 14 of the Mississippi River.-1/
VATER TAXON PERIOD TEMFERATURE EGGS-Freshwater dra Late May - Mid-June 57 - 72'F LARVAE
. Walleye /Sauger Mio-April 48 - 52*F Carp Late April 52 - 59'F Freshwater drum )
- I Cyprinidae (minnows) )
Cat.ostomidae (suckers) -) Late May - Late June 61 - 72*F Gizzard. shad )
White bass )
If H.E.S. 1979. Ichthyoplankton Studies. Chapte.r 8. Environuental Monitoring in the Mississippi River near Quad Cities Station. May 1975.through July 1978. Report to Commonwealth Edison Co., Chicago,
-Illinois. 74pp.
iO 123
Major components of the main channel fish assemblene in Pool 14 O
Table 2.
of the Mississippi River.
TAXON COLLECTION TECHNIQUE Acipenseridae (sturgeons)
Shovelnose sturgeon Trawl Clupeidae (herrings)
Cizzard shad Electroshocker Hiodontidae (mooneyes)
Mooneye Electroshocker-Trawl Cyprinidae (ninnows)
Carp Electroshocker-Trawl Silver chub Trawl Emerald shiner Trawl h River shiner Trawl Catostomidae (suckers)
River carpsucker Electroshocker-Trawl Smallmouth buffalo Electroshocker Bigmouth buffalo Electroshocker Ictaluridae Channel catfish Electroshocker-Trawl Stonecat Trawl Percichthyidae (temperate basses)
White bass Electroshocker Centrarchidae (sunfisbes)
Eluegill Electroshocker Largemouth bass Electroshocker h 124
Table 2. Continued O Electroshocker White crappie Black crappie Electroshocker Percidae (perches)
Sauger Electroshocker Walleye Electroshocker Sciaenidae-(drum)
Freshwater drum Electroshocker-Trawl O
ri 125
O atmosphere results in a small (generally absent) global-field and reduced far-field plume relative to the other seasons. In spite of the small extent of the heated areas relative to available habitat, most if not all species inhabiting Pool 14 could be attracted to temperatures exceeding ambient during this period. Numerous laboratory studies (McCauley 1977, Otto et al. 1975, Coutant 1975, Rice et d.1974, Barrans and Tubbs 1973, Coutant and Goodyear 1972) and field investigations (Yoder and Gammon 1976, Gibbons et d.197?,
Gammon 1971, Ferguson 1958) have demonstrated this attraction, raising the possibility that fish may seek out or be reluctant to leave the warmed areas a immediately downstream of the diffusers. Ir addition to the generalized dis-tributional shift. prolonged low level thermal experience during winter monchs would increase metabolic costs during a period of low food availability and potentially influence endocrine or metabolic aspects of the reproductive maturation process (Brungs and Jones 1977). Additional concerns specific to the winter period include cold shock and gas bubble disease. Both require that fish maintain residence within the confines of the heated areas for extended periods (days to weeks).
The general concern for body condition and reproductive impairment of fish that have access to unseasonally warm waters during the winter months relates particularly to those species, such as the yellow perch, for which a chill period is required for successful gonadal maturation (Brungs and Jones 1977, Mokanson 1977, Jones et d.1977, Hokanson et d.1973) . However, an elegant study of seasonal fish distribution in the vicinity of a thermal effluent has addressed this problem directly and done much to eliminate it as a pertinent concern for open-field discharges (Ross and Sinif 1980).
O 126 I
1
i l
F) u Ross and Sinif evaluated the movements of four species (yellow perch, walleye, northern pike and largemouth bass) in Pokegama Reservoir, Minnesota, an impounded section of the Mississippi River that receives a thermal efflvent from two 75 MWe generating units ( AT = 27'F). Most of the effort was directed tv Lhc yellow perch, a species with a mid-winter preferred temperature under laboratotf conditions of 54 to 65*F (McCauley 1977, Barrans and Tubbs 1973, Otto et al. 1975) and a winter chill period requirement for optimal spawning success of 185 days at 39'F or less (Jones et al. 1977). Observations on the walleye, northern pike and largemouth bass were restricted to a consideration of mobility and home range dimensions relative to the heated effluent.
The results are in accord with the intuitively obvious (but
\ difficult to confirm) concept that field distributions of fish reflect the interaction of numerous f actors, each having its own (dynamic) directional aspect and intensity (see also Kaufman et al.1980, Andrewartha and Birch 1954). Of the species studied, only the largemouth bass (two individuals) _
stayed within the thermally impacted area throughout the winter period.
Observations of walleye, northern pike and yellow perch demonstrated that factors other than or in addition to access to seasonally elevated tem-peratures were of impottance in determining distributions. Elevated thermal experience for these species was found to be transitory (incidental) in nature.
The more extensive evaluation of yellow perch distributions showed that only a small portion of the potentially impacted population experienced any (even a low level) increase in winter temperature exposure. Body size
}
127
(condition) and reproductive parameters (gonadal somatic indices) were 0
similar for perch collected from thermally impacted areas and adjacent, ambient temperature areas. The authors concluded that gonadal development and maturation (during the required winter chill period) are protected, even in the vicinity of a thermal effluent if the fish have access to thermally unaltered habitat. Certainly such a situation exists in Pool 14.
Several sid-winter fish kills at power plants have occurred, which can logically he attributed to cold shock following plant shut-down (Smithsonian Institution 1972, Commonwealth of Pennsylvania 1971, Trembley 1965). Such incidents are most likely to occur in situations in which a low velocity discharge is directed to a semi-enclosed embayment or canal or in water bodiea where the winter survival of exotic or introduced species is dependent on the presence of the heated effluent (for examp'.e, southeastern h reservoirs stocked with threadfin shad) . Neither situation is analogous to the Quad Cities Station, where high velocity diffusers are employed in an open-field context and where no thermally sensitive, exotic populations exist.
Fishes resident to Pool 14 are generally incapable of maintaining themselves within the diffuser near-fields for a sufficient period to acclimate (days). Most fish have long-term swimming capabilities (cruising speeds) of two to four times their body length (Otto et af. 1975, Webb 1975). In addition, swimming capability is reduced with both increasing size and decreasing temperatures. Assuming that most fish inhabiting Pool 14 are one foot or less in length (or that fish larger than one foot long have progressively reduced relative swimming capabilities) and referring to 128
t v
1
~,
the discussion by Dr. Kennedy (this volume) on the rates of temperature and velocity decay in the near-field plume, fish will generally be unab)e to experience elevated temperatures exceeding 4 to 8'F for more than brief
! periods. Available data on cold tolerance of fish species that occur in r Pool'14 (summarized in Brungs and Jones 1977) indicate that resident fishes can readily tolerate a decline of this magnitude should any individuals actually ondergo such acclimation (which we consider improbable - see also 3
Ross and Sinif 1980) and should it be necessary to reduce Station load or I shut down both generating units simultaneously, k
Prolonged exposure to elevated temperatures of 4 to 8'F during l= the vinter months could result in a coincident exposure to dissolved gas 3~ supersaturation levels of 110% at most (assuming the worst case situation:
' . O ty -
ambient water temperature of 32*F, water fully gas-saturated prior to condenser passage). This level of supersaturation is below that generally considered necessary to cause gas bubble disease (Otto 1976, Parametrix 1973). In addition, the effective level of gas supersaturation (that ,
existing where the fish are) will be substantially reduced by hydrostatic pressure (Klots 1961). Solubilities of gases (using solubility to imply a critical concentration above which a bubble can form) are approximately doubled for each 30 foot increase in water depth. Thus, fish within the Quad Cities diffuser _near-fields at elevated temperatures of 4 to 8'F but also at depths of greater than 3 to 4 feet will not experience effective gas saturation levels exceeding 100%.
Spri.ng: Spring is the period of maximum River flow and low to moderate air and water temperatures. The resultant rapid dilution and loss 129
of heat to the atmosphere prevent the development of a measurable global-field and strongly limit the areal extent of the far-field regions. Any prolonged exposure of fish to elevated temperatures is therefore unlikely to occur.
Spring is, of course, the spawning and incubation period for all but a few of the fishes that inhabit the Pool. The potential for entrainment of the spawn and early life stages into the thermal plume is considered in the following section.
Summca: Su=mer is the period of minimum flows and maximum ambient air and water temperatures. As such, rates of dilution and atmospheric cooling are minimized, and it is the seasonal worst case situation with regard to potential effects of elevated temperatures on resident fishes. During this period, the entire main channel of the river downstream of the diffuser may be warmed as much as 3.95'F. Specific concerns are (1) whether resident species are able to aurvive the maximum possible mid-suc:mer temperature rise of 4*F (to an approximate maximum value of 82*F), (2) whether global-field temperatures will exceed preferred levels (resulting in loss of habitat) and (3) whether growth of fishes residing within the global-field will be reduced, an indicat1on of less than optimal therr# conditions for various physiological functions (Brungs and Jones 1977).
The most compelling evidence that the fishery of Pool 14 will suffer no adverse effects as a result of warming of a portion of the main channel is the observation that all species of fish found to reside in the region potentially impacted by the globni-field plume have geographic distributions that extend considerably farther south than Pool 14 (Smith 1979, Eddy 1969), reaching latitudes where natural warming processes raise ambient mid-summer temperatures above 85'F. In other words, natural O
130
O populations occur further south in the Mississippi drainage under natural mid-summer conditions as severe or more severe than chose that could periodically occur in Pool 14 downstream of the diffusers under open-cycle operating conditions at the Quad Cities Station.
These concerns can also be addressed on the basis of existing field and laboratory studies, a less direct but more " conventional" procedure.
Maximum short term global-field temperatures (aabient or 78'F + 3.95*F or about 82*F) are well below mid-summer uppe.r lethal temperatures for all resident species that have been studied (Table 3, Brungs and Jones, 1977).
Maximur near-field temperatures (ambient 78'F + 23*F or about 101*F) exceed long-term lethal limits for most of the species. However, the areas (volume) involved are very small relative to available habitat, and fish will be O protected from harm by the high velocities as well as by innate, high temperature avoidance capabilities (Meldrium and Gift, 1971).
The mid-summer, global-field plume may exert some influence on fish distribution in the pool (however, see Ross and Sinif 1980). Final preferred temperatures as determined by laboratory and field studies are available for a number of species (Table 3). To the extent that fish distributions are influenced solely by temperature, these data indicate that 14 of the species studied (those with preferred temperatures of 86*F and above) might be attracted to the regica downstream of the diffusers even during the warmest months of the year, Five of the species for which data are available might b axpected to remain downstream of the heated region or move upstteam of the diffusers (those species with preferred temperaturet le9s than 86*F).
131
l Preferred temperatures, maximum weekly average temperatures for O
Table 3.
growth (MWAT) and ultimate upper lethal temperatures for fishes ,
occurring in Pool 14 of the Mississippi River.
Species Temperature (*F) .
1/ 3/ 1/
Preferred MWAT Lethal Carp 95 108 Longnose gar 95 River carpsucker 93 Buffalo 93 Bluegill 91 90 97 Largemouth bas 91 Quillback car 90 90 Channel catfish 90 90 100 Green sunfish 88 White bass 88 Gizzard shad 88 99 Skipjack herring 86 _
White crappie 86 82 Spotfin shiner 86 97 Bluntnose ninnow 84 90 Mooneye 84 Yellow Perch 84 3/ 4/ 2/
Walleye 80 84 93 3/ 3/
Northern pike 79 82 91 l_/ From Yoder and Gammon (1976) except as noted.
2_/ From Hokanson (1979).
3/ From Brungs and Jones (1977) except as noted.
9 4_/ Estimated from 1/ and 2_/.
132
9 U.S. EPA has recommended a procedure for calculating maximum
-. weekly average temperatures (WAT) acceptable for particular species based on the temperature that provides optimum or metabolically most efficient conditions for growth (Brungs and Jones 1977). The proposed calculation ist Optimum Growth l_ Upper Lethal Optimum Crowth
~
WAT= Temperature 3 Temperature Temperature The temperatures downstream of the Quad Cities Station for open-cycle operation are not expected to exceed 82*F after complete mixing of the cooling water dis-charge with river water. -This temperature is based on low flow conditions (7Q10) and 100% operating capacity. The species for which appropriate data are availabic are also shown in Table 3. Examination of the WAT relative to what is known about fish distributions and temperature exposures under field conditions (i.e., Barrans and Tubbs, 1973, Gammon, 1971, Ferguson, 1958) demonstrates the conservative nature of this parameter. Fish are commonly found to inhabit
- and flourish in environments as warm or warmer than this arbitrary limit for extended periods of time. However, the temperatures downstream of the Station to.which even the most sensitive species would be exposed would not exceed the WA1 for those species during extreme conditions of low flow and 100% Station operating capacity. Some species listed in Brungs and Jones,- 1977, such as the sauger, have recommended WAT's that are lower than those in Table 3, but these are believed to be due to artificial conditions associated with laboratory testing. There is a close correspond-I ence between preferred temperature and the WAT's, as would be expected on i
the basis of studies by Brett (1956), Strawn (1969,1961) and others, which
. relate preferred and optimum temperatures for a number of physiological
-criteria.. The general conclusions on distributional responses during summer l' months are unchanged.
133 l
FaLC. Fall is a period of intermediate flows and declining ambient air and water temperatures. As in spring, the global-fie?.d plume should be 9
greatly reduced or absent, and opportunities for prolonged exposure of fish to elevated temperatures are limited. On a single factor basis, near-field temperatures will be preferred over ambient levels (Table 3). However, the restricted areal extent of the plume as well as the expected tendency of local fish populations to respond in a distributional sense to the total environment rather than to temperature alone (Ross and Sinif, 1980) suggests that no measurable effects on the fishery of the pool should exist.
Maximum Ac:eptable Temperatures for Short-Term Exposures The diffuser system has been designed to promote very rapid dispersal of excess temperature by entrainment-mixing. However, as a consequence of this high velocity /entrainment process, some portion of the planktonic or freely drifting organisms moving down-river will be carried along with the mixing water and will receive some thermal dose. The nature of the dose depends on where in the cool 1ng sequence each organism is entrained as well as the path followed along the mixing gradient. Larger, free-swimming organisms may also receive a brief thermal dose as a result of unexpectedly encountering a shift in the current vector or local currents that exceed switzming capabilities.
Essccto of Jet Entuiment on Pfanktonic Foms: Jet entrainment at the dif fuser ports will subject fish eggs and larvae to both mechanical and thermal alterations. Mechanical alterations include shear forces and increased turbulence. No direct studies of the ef f ects of jet entrainment or shear /tur-bulence effects at levela comparable to those anticipated for the diffuser 6
134
g system (exit velocity of 8 to 9 f t/sec) have been performed. Morgan ci af. (1976) conducted laboratory studies of the effects of severe shear forces on the survival of striped bass and white perch eggs and larvae. Median lethal exposures for one minute periods exceeded 400 dynes 2/cm , a v.lue greatly in excess of that generated by a 9 ft/sec jet into standing water. Additional evidence for the insignificance of mechanical ef f ects due to jet entrainment at the dif fuser can be found in the studies of mechanically induced mortality as a consequence
~
of passage of eggs and larvae through power plant cooling systems. Mortalities of only 5 to 25% are typically reported for plant-entrained ichthyopiankton (Ginn e.t af. 1978. Ecological Analysts, Inc. 1977, Kedl and Coutant 1976).
Mortality predicted for plant passage (excluding lethal temperatures) at Quad Cities Station is less than 25% (H.E.S. 1978). Since both the time of exposure and the magnitude of the physical trauma acaotiated with plant g passage greatly excced those experienced by an egg or larva entrained at the diffuser jets, mechanical effects can logically be. discounted.
- Ichthyoplankton entrained into the diffuser near-field will suffer no adverse effects from the brief exposure to elevated temperatures. Substantial L numbers of fish eggs and larvae are present in Pool 14 from mid-April through late June at water temperatures ranging from 48 to about 72*F (Table 1).
Eggs or larvae subjected to the worst case exposure, entrainment at the b
diffuser port and transport down the plume centerline, will experience a 4 thermal dose as displayed in Figure 1. Maximum AT will be approximately 23*F, decaying as a consequence of entrainment mixing to about 4*F over a period of 13 to 24 seconds. This worst case situation is in no way reprc-sentative of the average thermal dose for the majority of entrained organisms.
9 135
Actual thermal doses will, for the most part, be much smaller in accord with the cooling bv dilution relation, which governs proportions of heated and ambient temperature waters making up successively cooler isotherms of the plume (see Carter et (14. 1977).
The most direct evidence that thermal doses experienced as a consequence of entrainment at the Quad Cities Station diffuser will have no effect on fish eggs and larvae is provided by the studies conducted at the station to evaluate ef fects of (total) cooling system passage (H.E.S.
1978). In these studies, ichthyoplankton were collected from the Station discharge canal, held at discharge temperatures for 8.5 minutes, cooled to ambient river temperature plus 3.5'F and examined for survival immediately and after 24 hrs. Proportions of live and dead larvae were compared with those for samples collected from the Station intake to determine the combined effects of mechanical abrasion-and thermal dose. Larvae examined included all species listed in Table 1 except valleye/sauger (tests were conducted in June following the walleye /sauger spawning period). Survival under these test circumstances and at discharge temperatures of 92*F or less ranged from 54 to 75% with no delayed mortalities in spite of the axtended holding time (8.5 min) and severe mechanical and collection stress imposed.
Further, similar studies conducted in 1979 (Commonwealth Edison Company 1980) have verified these observations and shown them to be conservative in that sampling procedures tended to adversely affect survival. Certainly the much smaller thermal dose (23*F to less than 4*F in 13 to 14 sec) and reduced mechanical stress associated with jet entrainment of ichthyoplankton into the near-field plume will have even less of an effect on survival.
9 136
_ - . - _~ _._ . _ . _ - - . _ _ - . . __
Ef fett.s of Jet Enttaistment of JuvenU.c and Adult Fisit: Juvenile or adult fish that encounter the near-field plume will experience no i physical damage as a consequence of jet entrainment. There are situations in which similar events have been shown to kill or damage fish. For
. example, j uvenile salmon entrcined into a ,4et (firehose) having an exit pressure of 100 psi were quickly killed (Anonymous 1957, cited in Bell et al. 1967), However, extensive literature reviews on the effects of fish entiainment by hydraulic turbines confirm that velocity changes of 8 to 9 f t/sec (maximum exit velocity at the' diffuser ports) is far below the critical level (see reviews by Bell ct ft.1967, Lucas 1962).
The brief thermal dose received by jet-entrained juveniles or adults will also not be sufficient to cause harm. This can be shown by calculating the length of time specific fish can tolerate an increase of 23'F above ambient river temperature following procedures and tolerance relations provided by the U.S. EPA (Brungs and Jones 1977). U.S. EPA recommends calculation of the length of time a particular species or life stage can survive a given temperature rise according to the relation:
log time = a + b (temp + 2) where a and b are the intercept and-slope respectively of the relation between test temperature and lethal temperature for a
~
i particular acclimation temperature.
1.
Using an ambient temperature of 77'El / (an approximation of the mid-summer maximum or worst case for heat tolerance), a temperature rise of t
1/
This value (77'F) is slightly -lover than the actual mid-su=mer maximum for-Pool 1* (78"F)'. . However, it is the closest temperature for which
(
values of a and b are available in Brungs and Jones (1977).
f 137 )
l _ , _ _ ,
23*F (maximum al for Quad Cities Station) and values for a and b taken from Appendix B of the U.S. EPA document, we obtain the limiting exposure times given in Table 4. Since the maximum time of passage is only about 14 seconds (the calculation ignores progressive cooling by dilution), it is clear that short-term thermal exposures of this type will not harm local fishes.
Conclusions The possible mechanisms and likelihood of harm to fishes resident to Pool 14 of the Mississippi River by heated water discharge at Quad Cities Station during open-cycle operations have been considered. Three potential means of exposure to elevated temperatures have been defined: jet entrain-ment of planktonic eggs and larvae, plume attraction of juveni.ie and adult forms and occasional long-term exposures (weeks) to low-level temperature increments of < 3.95'F. The potential for cold-shock and gas bubble disease have also been considered.
Data on fish occurreur.e and distribution obtained in the Quad Cities _
Monitoring Program (1969-present) and special studies conducted at the Station relating to thermal ef fects have been evaluated as have sources from the primary scientific literature. Procedures recoc= ended by the U.S.
EPA for evaluation of thermal effects have been employed. This effort has revealed no existing or i tential impacts on resident fishes associated with the thermal plume.
O 138
i 1
i Table 4. Maximum acceptable exposure times (mid-summer)1/ for juvenile and adult fish entrained at the Quad Cities Station diffusers. j Minimum Exceeds 2_/ 2/ Survival Maximum Species a b Time Potential min Exposure by Gizzard shad 47.1163 -1.3010 1.4* >SX Northern pike 17.3066 -0.4520 1.02 >4X Channel catfish Juvenile 34.5554 0.8854 1.68 >7X Adult 46.?l55 -1.2899 1.43 >5X Bluegill 23.8733 -0.6230 1.16 >5X Largerouth bass 26.3169 -0.6846 1.21 >5X Emerald shiner 26.7096 -0.7337 1.20 >5X 1/ Calculated according to Brungs and Jones-(1977), using an ambient temperature of 77'F (25'C).
2_/ Taken from Brungs and Jones'.(1977), Appendix B.
139
l O
Literature Cited Andrewartha, H.G. and L.C. Birch. 1954. The Distributicn and Abundance of Animals. Chicago, University of Chicago Press. 782pp.
Barrans, C.A. and R.A. Tubbs. 1973. Temperatures selected seasonally by four fishes from western Lake Eric. J. Fish. Res. Board Can.
30:1597-1703.
Bell, M.C., A.C. Delacy and G.J. Paulik. 1967. A Compendium on the Success of Passage of Small Fish Through Turbines. Report to the Fish. Eng. Res. Prog. U.S.C.O.E. 268pp.
Brett, J.R. 1956. Some principles in the thermal requirements of fishes. Quart. Rev. Biol. 31:75-87.
Brungs, W.A. and B.R. Jones. 1977. Temperature Criteria for Freshwater Fish: Protocol and Procedures. EPA-600/3-77-061. 130pp.
Carter, H.H., J.R. Schubel, R.E. Wilson and P.M.J. Woodhead. 1977. A rationale for evaluating thermally induced biological effects due to once-through cooling. Spec. Rept. 7. Mar. Sci. Res. Cent., St.
Univ. N.Y., Stony Brook, N.Y. 65pp. ggg Commonwealth Edison Company. 1980. Fish Egg and Larvae Special Studies.
In Quad Cities Aquatic Program. 1979 Annual Report. Vol. 1.
32pp.
Commonwealth of Pennsylvania. 1971. Water Pollution heport. No. 4170.
7pp.
Coutant, C.i . 1975. Temperature Selection of Fish - A Factor in Power Plant. Impact Assessments. IAEA-SM-187/ll. Oslo, 26-30 August, 1974.
Coutant, C.C. and C.P. Goodyear. 1972. Thermal effects - reviews. J.
Water Poll. Contr. Fed. 44:1250-1294.
Ferguson, R.E. 1958. The preferred temperature of fish and their mid-summer distribution in temperate lakes and streams. J. Fish. Res. Board Can.
15:607-624.
Ecological Analysts, Inc. 1977. Survival of Entrained Ichthyoplankton and Macro 1nvertebrates at Hudson River Power Plants. Report to Central Hudson Gas & Electric Co., Consolidated Edison Co. of N.Y. and Orange and Rockland Utilities, Inc. 228pp.
Eddy, S. 1969. How to Know the Freshwater Fishes. Dubuque, W.C. Brown Co. 286pp. gg l
140 l
Fry, F.E.J. 1971. The effect of environmental factors on the physiology of fish. In Fish Physiology. Vol. VI. W.S. Hoar and D.J. Randall (Eds.). N.Y., Academic Press.
] Gammon, J.R. 1971. The response of fish populations in the Wabash River to heated effluents. Proc. 3rd Nat. Symp. Radioecology. pp. 513-523.
Gibbons, J.W., J.R. Hook and D.L. Forney. 1972. Winter responses of largemouth bass to heated effluent from a nuclear reactor. Prog.
Fish. Cult. 34:88-90.
Ginn, T.C., G.U. Poje and J.M. O' Conner. 1978. Survival of planktonic organisms following passage through a simulated power plant condenser tube. In Proc. Fourth Nat. Workshop on Entrain. Imping. Chicago, Illinois, pp.91-101.
Hazelton Environmental Sciences Corp. (H.E.S.). 1978. The Survival of Entrained Ichthyoplankton at Quad Cities Station. 1978. Report to Commonwealth Edison Co., Chicago, Illinois. 59pp.
Hochachka, P.W. and C.N. Somero, 1971. Biochemical adaptation to the environment. In Fish Physiology. Vol. VI. W.C. Hoar and D.J.
Randall (Eds.). N.Y., Academic Press.
Hokanson, K.E.F. 1977. Temperature requirements of some percids and adaptations to the seasonal temperature cycle. J. Fish. Res. Board Can. 34:1524-1550.
Hokanson, K.E.F. , J.H. McCormick, B.R. Jones, and J.H. Tucker. 1973.
Thermal requirements for maturation, spawning and embryo survival of the brook trout, Salvellnus forttutalla (Mitchell) . J. Fish. Res.
- Board Can. 30:975-984.
Jones, B.R., K.E.F. Hokanson and J.H. McCormick. 1977. Winter temperature y re.quirements for maturation and spawning of yellow perch Perca flavcacena (Mitchell). In Towards a Plan of Actions for Mankind, Proc. World Conf., Vol. 3. Biological Balance and Thermal Modifications.
M. Marios (Ed.). pp. 189-192.
Kaufman, L.S., R.C. Otto and P.C. Miller. 1980. On distribution and abundance of juvenile fishes in the Upper Chesape.ake Bay. Chesapeake Bay Institute, The Johns Hopkins University. Spec. Rept. 78, Ref.
80-1.
Kedl, R.G. and C.C. Coutant. 1976. Survival of juvenile fishes receiving ther=al and mechanical stresses in a simulated power plant condenser.
In Thermal Ecology 11. G.W. Esch and R.W. McFarlane (Eds.). ERDA Symp. Ser. No. 40. Conf. -750425. 405pp.
Klots, C.E. 1961. Effect of hydrostatic pressure upon the solubility of gases. Limnol. and Ocean. 6:365-366.
9 141
Lucas, K.C. 1962. The Mortality To Fish Passing Through Hydraulir Turbines as Relat'ed to Cavitation and Performance Characteristics, Pressure Change, Negative Pressure and Other Factors. Symp. Cavitation and Hydraulic Machinery. Int. Assoc. Hyd. Res.
McCauley, R.W. 1977. Seasonal Effects on Temperature Preference in Yellow Perch Petta flavtScenS. EPA-600/3-77-0BS. 23pp.
Meldrim, J.W. and J.J. Gift. 1971. Temperature preference, avoidance and shock experiments with estuarine fishes. Ichthyological Associates, Bull. 7. 75 pp.
Morgan, R.P., R.E. Ulanovicz, V.J. Rasin, L.A. Noe and G.B. Gray. 1976.
Effects of shear on eggs and larvae of the striped bass and the white perch. Trans. Am. Fish. Soc. 105:149-154.
Otto, R.G. 1976. Thermal effluents, fish and gas bubble disease in southwestern Lake Michigan. In Thermal Ecology 11. G.W. Esch and R.H. McFarlane (Eds.). ERDA Symp. Ser. No. 40. Conf. - 750425. 405pp.
Otto, R.G. , J. Rice and M. Kitchel. 1975. Temperature effects on fish.
In Evaluation of Thermal Effects in Southwestern Lake Michigan. Special Studies 1972-1973. Report to Commonwealth Edison Company, Chicago,
"nois. 96pp.
Parametrix, Inc. 1973. Resource and Literature Review. Dissolved Gas Supersaturation and Gas Bubble Disease. Rept, to N.W. Utility Coop.
Boise, Idaho. 60 pp.
Rice, J., J.F. Krueger and R.G. Otto. 1974. Laboratory fish studies. In A Baseline / Predictive Environmental Assessment of Lake Wylie. Report to Duke Power Company. Charlotte, N.C. 142pp.
Ross, M.J. and D.B. Sinif. 1980. Spatial Distribution and Temperature Selection of Fish Near the Thermal Outfall of a Power Plant During Fall, Winter and Spring. EPA-600/3-80-009. 117pp.
Smith, P.W. 1979. The Fishes of Illinois. Urbana, Univ. of Illinois Press.
313pp.
Smithsonian Institution. 1972. Report of the Center for Short-Lived Phenomena. February.
Strawn, K. 1969. Beneficial uses of warm water discharges in surface waters. In Electric Power and Thermal Discharges. M. Eisenbud N.Y. , Gordon and Breach Sci. Pub. 423pp.
and G. Gleason (Eds.) .
Strawn K. 1961. Growth of largemouth hass f ry at various temperatures.
Trans. Am. Fish Soc. 90:334-335 O
142 l
Trembley, F.J. 1965. Effects of cooling water from steam electric plants O on stream biota. In Biological Problems in Water Pollution. Third Seminar. Dept. H. E.W. , U . S . P . ll. S . Cincinnati, Ohio. 307pp.
Webb, P.W. 1975. Hydrodynamics and entgetics of fish propulsion. Bull.
190. Fish. kes. Board Can. 158pp.
Yoder, C.O. and J.R. Gammon. 1976. Seasonal distribution and abundance of Ohio River fishes at The J.M. Stuart Electric Generating Station.
In Thermal Ecology II. G.W. Esch and R.W. McFarlane (Eds.). ERDA Sump. Ser. No. 40. Conf. - 750425. 405pp.
O O
143
9 Section III 316(b) Demonstration Supplement 9
9
V l0 '
Table of Contents Title- g Table of Contents i Introduction 144 A .' Entrain:nent Studies 145 B. Impingement Studies 155 LO l
l' i
l :_
l 1
I.
i l
! .s l
O i
l'
~
Introduction h
This section is an update of the Demonstration previously submitted to Region V, U.S. Eavironmental Protection Agency (USEPA) by Commonwealth Edison Company on April 10, 1975, under Section 316(b) of the Federal Water Pollution Control Act (FWPCA).
Results of studies conducted in 1972-1973 to evaluate the effects of entrainment on phytoplankton, zooplankton and macroinvertebrate drift were presented as part of the original 316(a) Demonstration submission in 1975.
Special studies conducted during 1974 to determine ways of minimizing impinge-ment at Quad Cities Station were also presented in the original 316(b) Demonstra-tion. .
Since submission of the original 316(b) Demonstrations, several studies have been conducted to do:ument the effects of npen cycle operation on organisms entrained in condenser cooling water. Also studies have been undertaken to evaluate methods to minimize impingement and to quantify impingement losses relative to fish population levels in Pool 14. These special studies included investigations to document the effects of open cycle operation on entrainment (phytoplankton, zooplan' ton and macroin-vertebrate drift) during the low flow year of 1976; investigations to define more precisely the effects of condenser passage on ichthyoplankton; and a study to evaluate the effectiveness of a barrier net located at the river's edge of the intake forebay in minimizing impingement.
O 144
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p.
I ir i
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A.- Entrettuent Studies
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> _ 4 %.. , m- are, -# . =ne we..---e +--e< = . - - we+.-a--a m..- . = w --e-w+***wt"*->v-e"r"-teNfw'wt"twvt
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O Table of Cortents Ti t_l e_
14$
Entrairmect Stunes Phytoplankton and 2.coplankten 145 1.
147
- 2. Macroinvertebrate Drift 147
- 3. Ichthyopiankton 154 Literature Cited 9
9 i
1 A. Entrainment Studies, Several reports form the basis of this summary. Entrainment studies conducted during 1972 through 1973 and 1976, are reviewed in the rerort en-titled, "Preoperational and Operational Environmental !!onitoring in the .
l Mississippi River near Quad Cities Station, August, 1969 to December. l 1978" (Hazleton Environmental Sciences, 1979a). That ret. ;t also discusses ichthyoplankton impact assessments. Special ichthyoplankton studies defining the effects of entrainnent are discussed in three reports "The l Survival of Ichthyoplankton at Quad Cities Station" (Hazleton Environmental Sciences. 1979b), " Intensive Ichthyoplankton Studios at Quad Cities l Station, June,1978" (Eazleton Environmental Sciences,1979c) and " Quad ;
Cities Station Aquatic Program,1979 Annual Report" (Commonwealth Edison 4
Company, 1980).
0 1. Phytoplankton and Zooplankton This summary is based on Hazleton Environmental Sefences ;
-:(1979a pp.-3.31-and 3.32-and 4.24 to 4.26). In 1976, as in the earlier studies.effecc.s of condenser passage on phytoplankton were evident but somewhat incensistent. In spite of the reductions in phytoplankton abundance and .hlorophy11.a concentrations noted in the discharge. bay,_
slight increase.* were observed at locations in the river immediately
-downstream of the diffuse, discharga. Thus the net effect of condenser passage on phytoplankton does not constitute an adverse impact on the river, i
O I 145 ,
o
The ef fect of entrainment on the total cormunity passing the St tion was assumed to be directly related to cooling water divertcd through the Station. During all previous entrainment studies (1972-1973) the Station used a maximum of 9% of the river for condenser cooling.
On the date or the 1976 study, however (a period of extraordinarily low flows) almost 13% of the river's flaw was estimated to pass through the Station. Projected total river effects during river flows in excess of 23,000 cfs reached an estimated peak of G% and averaged less than 1%
reductier. of total phytoplankton productivity during 1972-1973 (two unit open-cycle operation). 1.ess than 1% reduction during the icw flow sampling period (one unit open-cycle operation) was recorded in 1976.
Results of the zooplankton entrainment studies indicated mortalities associated with pacange through the condensers never reached 100% and the percentage of the total river zooplankton killed was very small. During the 1972-1973 period, it was estimated that the maximum percentage killed for two unit open-cycle operation was 4.4%. For the low flow period in 1976 when only one unit was operating open-cycle, approximately 2.1% of the river's zooplankton community was killed.
The projections for the plankton conmunity ignore the natural resiliency of plankton communities to reductions in numbers resulting from such occurrences as passage through a condenser cooling system.
Rapid compensatory response is a result of high reproductive rates and short generation times of plankters.
146
i i
t g 2. Macroinvertebrate Drfft
{-w/
- s. r i
This summary is based ou Hazleton Environmental Sciences (1979a ;
pp. 6.123 to 6.124). Studies conducted during the low flow period in 1976, i
were limited to measuring macroinvertebrate drift densities at locations !
upstream and downstream of the diffuser pipe discharge within the area of the mixing zone. No significant changes were observed in the drif t passing ,
s across the mixing zone of the diffuser pipe system in the Mississippi River.- Mortalities for the macroinvertebrate drif t assemblage increased about 4% af ter passage through the area of thermal discharge; these increases j were not statistically significant and-could just as easily have been a result of sampling mortality and natural variability.
- 3. Ichthyoplankton This summary is based on reports by Hazleton Environmental Scieuces (1979a. pp. 8.1-74 and 1979b.c) and Commonwealth Edison Company (1980, pp. 2-1 through 2-32). In the initial entrainment attdies conducted in 1975 and 1976 at Quad Cities Station, it was estimated that- as much as 10% of the total ichthyoplankton drif t was being entrained during actual Station operation. I Turther most of the entrainment occurred during closed or partial closed-cycle i
operation (RALCO Environment Sciences, 1977, p.-479). This implies an even 7 greater percentage would be . N t for open-cycle cooling. During 1978, a
~
= review of the methods, sample locations and assumptions used in deriving
- . .these estimates indicated that they were undoubtedly much greater-than actus1 entrainment. The high initial estimate was due to unrepresentat ve, high. ,
l L ichthyoplankton densities at the sampling location used to estimate entrainment densities. This sampling loc.ation was situated immediately downstream of
.O .
147
a barge ramp, upstream of the intake, in a calm current-free area. Dye studies indicated that intake water was not withdrawn from this area as O
originally anticipated.
In 1978, special studies were undertaken which had as one of their objectives, estimates of entrainment based on sampling immediately in front of the intake and in the discharge bay as well as at the location used to make entrainment estimates in 1975 and 1976 (Hazleton Environmental Sciences, 1979b). Abundance at locations immediately in front of the intake and in the discharge were shown to be substantially less than at .he quiescent location used for estimating entrainment in 1975 and 1976.
These studies also found that densities in the discharge canal were lower than those in front of the intake end it was suspected that dencities of ichthyoplankton at the discharge location may provide the most accurate estimate of the density of entrained ichthyoplankton. However, entrainment e
abuncances were conservatively based on those abundances at the location in front of the intake rather thae on fischarge samples.
The special 1978 studies also had as an objective the evaluation of survival of entrained ichthyoplankton (Hszieton Environmental Sciences,1979b,c).
These special survival studies were conducted because previous estimates of en-trainment losses assumed a 100% rertality of entrained ichthyoplankters. Recent studies at other steam electrtc generating stations indicated that this was not likely to be the case. Consequently, entrainment survival was documented at various Station operating power levels during open-cycle cooling. Entrainment survival of total ichthyoplankton ranged from 63 to 72% when discharge wat-temperatures were below 90.5'F (32.5'C) and decreased to 40% when dischan;<
O 148
l l
r
- ( )- water temperatures ranged from 90.5 to 91.4'F (32.5 to 33'C). Lowest entrain-ment survival occurred when the Station was operating at full power capacity (96 to 99%) and discharge temperatures exceeded 100.2'F (37.9'C). Evaluations j of river and Station operating data for 1975 through 1978, however, indicated ,
r that greater than 80% of the ichthyoplankton drif t pass the Station intake t
prior to discharge temperatures reaching 91.4*F (33.0*C).
6 In light of these special studies, the ichthyoplankton abundance data were used to estimate the percentage ichthyoplankton drift past the Station lost due to entrainment from 1975 through 1978 (Harleton Environmental Sciences, 1979a, pp. 8.57-67). Only these years were included in the analysis because the sampling design used in the river to estimate abundance was more consistent than during earlier years.
() The total ickthyoplankton drif t for Pool 14 in the vicinity of Quad Cities Station betwt a 1975 and 1978, was estimated to range from 3.0 x 109 to 13.5 x 109 individucts. Freshwater drum comprised 66-98% of all fish eggs collected. Typically, freshwater drum, carp and minnows were the most abundant taxa of ichthyoplankters. Ichthyoplankters were typically present in the drif t by mid to late April each year, and the greatest number of ichthyoplankters were usually found in the drift prior to mid-June.
e i Based on abundances at river locations either immediately adjacent '
to or upstream of the forebay, estimated annual total ichthyoplankton losses from 1975 through 1978, during actual Station-operation would have amounted to 1,3-3.1% of the ichthyopienkton drift. Actual Station operation was based on the daily cooling cycle mode of operation which varied from closed or partial open-cycle and to a much less degree, open cycle.(Hazleton Environmental O Sciences 1979a, Table 8.13).
l L
j 149
The estimated percentage of the total river ichthyoplankton loss g due to entrainment was also projected for open-cycle c,peratf or, for each year 1975 through 1978, and it was estimated it would have ranged from 1.6-5.4%
(Itazleton Environmental Sciences,1979a, Table 8.14). Highest percentage of entrainment losses would have cecurred during the low flow years of 1976 and 1977. Based on average weekly Station loads and ambient temperatures for the months of April through June,1975 through 1978, the majority of entrained ichthyoplankters would survive intake entrainment since the estimated maximum discharge temperatures were below 90.5'F (32.5'C).
Two sources of variation were identified during the course of the special studies in 1978, which suggested that a potential for further improve-ment in the estimate of entrainment mortality may be possibic. First, as mentioned earlier, larval densities measured at river locations immediately in front of the intake and used to estimate entrainment in 1978, appeared e to over-estimate those actually observed within the Station discharge bay by a significant margin. Discharge densities, presumably a direct measure of numbers of larvae which had passed through the cooling system, were as much as 30% less than at the locations used to estimate entrainment abundance in the 1978 studies. While it was assumed that the extremely turbulent conditions at the sampling area in the dischargr 'nsured thorough mixing, this assumption was not tested in 1978, and it mav a been possible that spatial variation within the discharge bay was responsible for the observed differences.
Second, it was noted that a portfor of the dead larvae collected ~
f rom the Station discharge in the survival studies had assumed an opaque appearance associated with tissue deterioration. In the 1978 study, the 9
150
l
() density of opaque larvae was higher in the discharge than in the intake. These density dif f erences resulted in a decrease in survival estimates sinec all dead larvae were used in estimating survival. The short time required for a larvae to traverse the cooling syster did not seem adequate for such degenerative changes to take place. This suggested that the fraction of dead larvae collected from the discharge which were opaque had actu111y been dead prior to entering the cooling system and should be excluded from estimates of Station induced mortality. However, unexplained differences between densities of dead opaque larvae co?.lected from the discharge and from a single, mid-depth location in the intake forebay prevented such a correction for the 1978 data set. Therefore, estimates of survival in 1978, were based on ,;-
use of both transparent and opaque dead ichthyoplankton.
Studies were designed and conducted in 1979, to evaluate these sources O of variation in estimates of fish egg and larvae entrainment and survival at Quad Cities Station (Commonwealth Edison Company,1980, pp. 2-1 through 32).
Thcee included further investigations as to which location was most appropriate for estimating entrainment abundances and whether opaque larvae should be included in mortality estimates. Comparisons were made of net collections at the river location in f ront of the Station intake forebay and at three cross sectional transects in the discharge bay. The river location was found to be a poor basis for making estimates of entrainment in terms of species composition, abundance of various taxa and abundance of specific life stages within taxa. Egg and larval densities at the river location were consistently higher than densities in the discharge.
The single known contradictory explanation for these dif f erences was the possible destruction of eggs or larvae during the course of passage (v) :
151
through the coeling system. This consideration was disregarded because of the results of the survival study. In addition to the many larvae surviving passage througl the Station, careful examination of larvae collected revealed very few mechat teally damaged individuals. It was concluded then that entrainment abundances were lower than what would be predicted based on larval abundances at the intake location. Densities of total larvae at the discharge bay location were about 20% lower than the river location.
With respect to the opaque larvae evaluation from the laboratory studies conducted in 1979, it was concluded that larvae killed by passage through the condensers at t*mperatures below 91.4*F (33'C) and collected from the discharge bay do not turn opaque in the time it takes to collect and examine the samples sud thus opaque larvae can be excluded from entrainment mortality estimates (Cocunonwealth Edison Company, 1980). The relationship between water temperature and time to opacity for recently killed larvae (transparent dead larvae) as determined in this study showed that, at discharge temperatures of lesh than 91.4*F (33'C), more than 30 minutes are required for the development of opacity. The time required for a larvae to traverse the uooling system is 8.5 minutes. The study also showed that differences in the densities of live larvae and dead, opaque larsae observed between the intake forebay and tha discharge bay in 1978, can be explained by spatial variability at the two locations. Thus, the true survival below the critical temperature of 91.4*F (33*C) would be greater than the 40 to 72% reported in 1978. A re-evaluation of the 1978 data sugusts that the increase in survival would range from 2-12%.
O 152
It was also concluded that there were little meaningful differences between estimates of ichthyoplanktors lost due to open cycle operation and the present operating mode (partial-open cycle) where the volume of river water used for make-up is increased when the return water from the spray canal exceeds 93*F (34.0'C). Small differences result between these two operating modes ever though 50 to 80% less water is withdrawn from the river during partial open-cycle operation, because it can be assumed that all ichtho-plankters entrained during this operating mode vould be lost as discharge temperatures would exceed 91.4*F (33'C).
lO l
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.153 l
o e
Literature Cited Cormonwealth Edisot. Company,1980. Quad Cities Aquatic program, 1979 ,
Annual Report. Chaptern 1 through 5 and Appendices A, B, C D and E. ,
lla:.;1eton Environmental Sciences,1979a. Envirenmental !!anitoring in the Mississippi River near Quad Cities Station, August 1968 to December 1978. Chapter 1 through 8 and Appendices A, B, C and D.
1979 b. The Survival of Entrained Ichthyoplankton at Quad Cities Strtion, June 1978. 11ES !!o. 550105739.
55 pp.
1979 c. Intensive Ichthyoplankton Studies ar. Quad Cities Station, June 1978. IIES No. 55105739.
O l
9 154
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O Table of Contents Title Page List of Figures 11 List of Tables iii Resulte of Impingement Sampling 155 Impingement Exploitataon 159 Commercial Fish Harvest Freshwater Drum Life History and 171 Population Dynamics Study 171 Barrier Net Studies 178 Literature Cited 181 9
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List of Figures ,
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1 Estimated number of fish impinged at Quad-Cities Station from 1973 :
through 1979 156 l.
2 Estimated weight of fish impinged at Quad-Cities Station from 1973 through 1979 157 P
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O List of Tables Table No. Title Pg 1 Standing crop catimates for rotenone surveys in Pool 14 of the Mississippi River with comparisons to other Mississippi River Surveys 161 2 Results of Mark-Recapture study using electroshocking to determine collection efficiency of roteaone surveys in Pool 14, Mississippi River near Quad Cities Station. 163 3 Impingement exploitatian rates at Quad Cities Station based on total estimated standing crop only for Slough-Lake habitat in Pool 14 of the Kississippi River, 1973 through 1979 165 4 Impingement exploitation rates at Quad Cities Station for gizzard shad based on estimated standing stocks for Slough Lake habitat in Pool 14 of the Mississippi River, 1977 through 1979. 167 5 Impingement exploitation rates at Quad efties Station for channel catItsh based on estimated standing stocka for Slough-Lake habitat in Pool 14 of the Mississippi River, 1977 through 1979. 168 6 Impingement exploitation rates at Quad Cities Station for bluegill based on estimated standing stocks for Slough-Lake habitat in Pool 14 of the Mississippi River, 1977 throug'a 1979. 169 O
iii d
i I
i Table No. -Title page !
7 Impingement exploitation rates at Quad Cities Station for white bass based on estimated standing stocks for Slough-Lake habitt , in Pool 14 of the Mississippi River, 1977 through 1979. 170 8 Estimates for Age Class 0 and 1 Freshwater Drum from Backcalculation of 1980 Population Estimates. 175 9 Impingement Exploitation Estimates for Age Class 0 and 1 Freshwater Drum at Quad-Cities Station from 1973 through 1960. 177 l
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B. Impingement h
This summary is based on Hazleton Environmental Sciences (1979a pp.
- 7. 74 to 7.123) and Commonwealth Edison Cot.pany (1980 pp. 4-1 to 4-27) . Impinge-ment studies have been conducted at Quad Cities Station since 1973. Results considered in this summary cover the period 1973 through 1979. The total number and weight of fish estimated to be impinged at Quad Cities Station each year is shown in Figures 1 and 2.
Annual impingement estimates for the 3 ears 1977 and 1978 were substantiolly less than the estimates presented in the 1976 annual report (NALCO Environmental Sciences, 1977, pp. 343-351) for the period 1973 through 1976. The differences between the 1977-1978 annual estimates and those annual estimates presented in the 1976 report for the years 1973-1976, prompted a review and recalculation (Adjusted Patio Estimator) of the original Ratio Estimators (RE) on which the years 1973-1976 annua 1 impinge-O ment estimates were based.
The Ratio Estimator was developed for the years 1973-1976, because the mesh size (1" x 3-3/4") of the trash basket used to collect impinged fish in these years was larger than that of the traveling screens (3/8" x 3/8") and many of the smaller impinged fish were believed to be lost from the basket. Prior to initiation of impingement studies in 1973 when the Station was operating open-cycle, small mesh baskets (3/8" x 3/8") were used tn collect impinged material. These baskets proved unsatisfactory because leaves and debris often plugged the small openings causing the baskets to overflow, thus, making the data unreliable. The small mesh basket was replaced O
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with the large mesh basket in 1973 and continued ;o be used through January,
(" p 1977 when it was again replaced with a small mesh (3/8" x 3/8") basket.
The naaller mesh size basket was installed at this time because the Station was operating closed or partially closed-cycle which resulted in lower drbris loading in the basket. To determine the extent that smaller fishes were passing through the larger mesh, the catches of small and large mesh baskets were compared during special studies conducted in 1973 and 1976, and a conversion f actor or " Ratio Estimator" (RE) was calculated on a monthly basis. The monthly RE's were averaged and this value was multiplied by the annual estimate of impingement to correct for losses through the large mesh basket. ,
It was concluded after reviewing the'1977 and 1978 impingement l l
- data, when small mesh baskets were used, that the earlier monthly RE's should not i be developed solely on a monthly basis, or averaged and multiplied by the actual annual impingement sinca - impingement varies with biological changes in the fish population rather than by artificial chanp.es based oa calendar -r eventa. For example, by November, fish were large enough to be retained !
l by the large mesh basket and it was inappropriate to correct for losses based on summer impingement. As a result, the monthly RE's were adjusted (ARE) to account for biological changes which occurred.within or among calendar months. Within each year, the actual impingement catches were expanded to monthly estimates which_were summed to estimate annual impinge-ment _(Hazleton Environmental Sciences.1979a pp. 7.74-97).. ,
l T' presence of the spray canal return water in the area of the j
- . forebay probably explains differences in annual impingement numbers between LO 158
1973, when the Station was operating npen-cycle and 1974-1979, when the Station generally operated closed or partial closed-cycle. During closed-cycle O and partial closed-cycle, a small portion of warm water from the spray canal leaks from the intake bay into the river. This warm water appears to attract fish in the fall and winter. During the summer months, however, the warm return water from the spray canal in the intake bay probably results in fish avoidance of this area. Impingement was very high in the summer, 1973, com-pared to the remaining years when opet-cycle was no longer used. During 1973-1976, the annual total estimated weight did not vary appreciably between open (1973) and closed or partial closed-cycle (1974-1976). In 1977 and 1978, however, much higher total annual weights of fish impinged were estimated even though total numbers remained less than 1973 levels. This was probably due to impingement of largcr sized fish later in the year because of attraction to the intake forebay, and avoidance of the warm water tem-peratures in the forebay as smaller individuals in the summer.
O During the seven years of study, seventy-five species of fish have been identified with gizzard shad and freshwater d: n comprising almost 90%
of the total numerical catch. Species composition during the period 1973-1979, has been similar with gizzard shad and freshwater drum, the two most abundant species and channel catfish and white bass generally among the five most abundant species each year.
Impingement Exploitation The purpose of this section is to compare impingement losses with estimated standing stocks in Pool 14. The ratio of impingement loss (weight)
O 159
-..-..- - -.- - -.~ .- - .-.-. - . - - - - .-.- -_- ~ _ - - - - - . -
l to estimated standing stock is considered f or this sumary to be impingement mploitation (or percent impinged) except as noted. Estimates of standing stock were derived from several sources. The standing stock ,
of fish in Pool 14 of the Mississippi River was estimated to be 356 lbs/ acre with a multiple regression analysis as developed by Jenkins and described in NALCO Environmental Sciences,1977 (p. 371). Cove or backwater rotenone surveys were conducted near the station during 1977 (Muench, 1978) and 1979 (Commonwealth Edison Co., 1980) and yielded an estimated at.inding stock of 566 lbs/ acre in 1977, and 648.9 lbs/ acre in 1979.
In addition to the studies conducted near the station in Pool 14, several other standing stock' estimates have been made for_the Mississippi River
~
backwaters using the backwater or cove rotenone sampling technique.
Results of the various studies including those near the station are presentad in Table 1.
Standing stock estimates in most of the other studies were in general, considerably less than the Pool 14 rotenone study estimater. .hese lower estimates may have resulted from incomplete recovery of fish. For example, of the four surveys described by Christenson and Smith (1965), only one utilized recovery af marked fish to estimate collection efficiency (Area B in Pool SA). In that survey, only 16_ fish representing 8 species were marked and released prior to rotenone application. Because all 16 fish were re-covered, it was assumed that'in the remaining surveys there was complete In recovery of fish, thereby depicting accurate standing stock estimates.
the rotenone _ surveys conducted near the Station, a much greater number of
. fish were marked and released prior to application of rotenone than was recorded in the Christenson and Smith surveys. Results are presented in
- O ,
160
Table 1. Standing Crop Estimates for Rotenone Surveys in Pool 14 of the Mississippi River with Comparisons to Other Mississippi River Surveys h
Location Average Data Source Survey Method (Pool l' umber) Ibs/A Cornonwealth Rotenone and 14 648.6 Edison Co., Mark-Recapture using (1980) Electrofishing Muench, (1978) Rotenone and 14 366.0 Mark-Recapture using Electrofishing 1/ 2/
Christenson Rotenone- 5-A 324 . CT-and Smith, (1965)
UMRCC, (1948) Rotenone 18 390.6 (Oguawka-1)
UMRCC, (1948) Rotenone 18 694.6 (Oguawka-2)
UMRCC, (1947) Rotenone 13 171.4 (Savanna-1)
UMRCC, (1947) Rotenone 13 422.8 (Savanna-2)
- 1. Mark and recapture procedures used during 1 of 4 surveys at this location
- 2. Average of four surveys 0
161
Table 2. In 1977, 88 fish of 8 species were captured, marked by fin clipping and released inside the sampling area. 7n 1979, 278 fish of 10 species were fin clipped and released inside the sampling area. In contrast to results reported by Christiansen and Smith during both the Muench, 1977
=
survey and the Commonwealth Edison Company 1979 survey, recovery of marked fish was low, 25.0% and 32.4%, respectively. Consequently, actual numbers and weights of fish collected af ter poisoning each area were adjusted to reflect the percentage of marked fish released that were recovered, thereby resulting in much higher standing stock estimates on both a total and species basis.
Based on the various standing stock estimates in Table 1, conservative or over-estimates of impingement exploitation rates at Quad Cities Station from 1973-1979 of the Pool 14 fishery have been made using only O the combined total slough-lake habitat in Pool 14 and multiplied by slough standing stock estimates. Only the slough-lake habitat standing stock estimates were used because expanding the present data base for all habitats is not appropriate given the differences that would be expected to occur between the slough-lake habitat and other habitats. Because differences in standing stock between habitats is expected, a more reliable approach would be to stratify projections by habitat type if standing stock estimates for other habitatt were available. With the present data base, however, it is possible to reliably estimate standing sto:ks only for the slough-lake _ habitat in Pool 14.
The total surface area of Pool 14 is 10,410.7 acres, of which 41.0 percent or 4267.7 acres represents the slough-lake habitat (Helms, O
162
Table 2. Results of Mark-Recapture Study Using Electroshocking to Determine Collection Efficiency of Rotenone Surveys in Pool 14, Mississippi River near Quad Cities Station Year Nunber Fish Number Marked %
Location Marked and Released Fish Recovered Recovered Sampled Data Source RM 511.5 88 22 25.0 1977 Meunch (1978)
Comonwealth RM 511.8 278 90 32.4 1979 Edison (1980) 5 m
- 9 e
..._ ___ _ ._ _ _ . _ _ _ . . _ . _ _ _ _ . _ _ . _ - . . - ~ _ _ . _ . _
i 1968). Using the average estimate of 459.7 lbs/ acre presented in Table 3, the total standing stock for the slough-lake habitat in Pool 14 is estimated to be about 2.0 x 106 Pounds, Exploitation rates were estimated to range from 0.4 to 3.J percent for the years 1973 through 1979. The lowest impingement exploitation rate was estimated for 1979, and attributed to placement of a barrier aet in front of the intake forebay to minimize impingement (this section). However, estimated impingement exploitation rates still only range from 1.1 to 3.3 percent for 1973 through 1978.
Standing stock estimates of four of the five most abundant impinged species (gizzard shad, channel catfish, bluegill and white bass) recorded in impingement samples were estimated for the slough-lake habitat in Pool 14 (Tables 4-7). The second highest impinged species was freshwater drum, which is addressed in greater detail later in this section.
(I Impingement exploitation-was estimated for 1977 through 1979 for each species. The years 1977 through 1979 were selected for comparison because annual impingement estimates for the individual species are available for these years while they are not for the earlier years 1973 through 1976.
As discussed previously,- for the years 1973 through 1976, only total anne:
impingement (all species combined) was estimated (Hazleton Environmental ,
Sciences, 1979a). ;
For the four species annual impingement exploitation rates ranged from 0.4 to 8.9 percent for gizzard shad, 0.3 to 2.4 percent for channel catfish, 0.3 to 0.4 percent for bluegill, and 1.1 to 10.9 percent for white bass (Tables 4 through 7). These estimated exploitation rates -
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Table 3. Impingement Exploitation Rates (Percent) at Quad Cities Station Based on Total Estimated Standing Crop Only for Slough-Lake Habitat in Pool 14 of the Mississippi River, 1973 Through 1979 b
Estimated Exploitation Rate (Percent)
Estimated Standing Crop Estimated Weight Impinged (1?-)
1973 1974 1975 1976 1977 1978 1979 27,045 63,998 48,245 7,494 Data Source Ibe/ Acre Total (Ib) 25,615 21,833 24,251 Commonwealth Edison Co. , (1980) 648.6 2,768,030 0.9 0.8 0.9 1.0 2.3 1.7 0.3 1.1 0.9 1.0 1.1 2.6 2.0 0.3 Muench (1978) 566.0 2,415,518 Christenson and Smith (1965) 324.0 1,382,735 2.0 1.6 1.8 2.0 4.6 3.5 0.5 w
8l UMRCC (1947)
Savanna-1 171.0 729,777 3.5 3.0 3.3 3.7 8.8 6.6 1.0 1.3 1.5 3.5 2.7 0.4 Savanna-2 423.0 1,805,237 1.4 1.2 UMRCC (1948)
Oquawka - 1 390.6 1.666,964 1.5 1.3 1.5 1.6 3.8 2.9 0.4 0.7 0.8 0.9 2.2 1.6 0.3 Oquawka - 2 694.6 2,964,344 0.9 c
Average 459.7 1,961,862 1.3 1.1 1.2 1.3 3.3 2.5 0.4
- a. Total based on 4,267.7 acres slough-lake habitat in Pool 14
- b. Percentage calculated by dividing estimated weight impinged by total estima*.ed standing crop for slough-lake habitat.
- c. Averase of estimates of standing crop presented in various senrces of da ta.
- 9 e
. . . . ~ . - - _ - - ..... ~ . - . _ . - - - . - - - . -.-_. - - . -
i for all specica are believed to be conservative because the standing i stock estimates on which exploitation rates are based, are only for the ;
i slough-lake habitat in Pool 14. This is especially true for gitzard shad and white bass which are common to all sampling locations in Pool 14 (Commonwealth Edison Company,1980, Tables 3-3 and 3-7) . Since both of these species are common to the main channe3 and side channel habitats, in addition to backwater areas, standing stock estimates on an individual species sasis would undoubtedly >
be much greater if considered on a pool vide basis.
The exploitation rate ranges discussed above vill not measurably affect the Pool 14 fishery. In a review of many published commercial and sport fishery exp?'itation rate estimates McFadden (1977) reports that it is not uncommon for > 25% of the exploitable age classes in a population to be removed annually for a period of time spanning decades while at the
) same time these fish stccks continue to operate at maximum product 1vity.
Of particular interest are exploitation rates of freshwater drum, channel catfish and bluegill populations. McFadden cites literature indicating ar.nual commercial and sport fishery exploitation rates ranging from 31 to S8 percent for freshwater drum, 30 percent for channel catfish, and 15 to 42%
for bluegill (see Table 2, pp. 173 through 175 in McFadden, 1977).
These estimates of compensable exploitation reviewed by McFadden are .
based on older fish. When class-0 and I fish are considered, it is likely that l
for a highly fecund and short-lived fish such as the gizzard shad, that com-l pensable exploitation rates could be even higher than 25%. Thus, it is note-worthy that impingement at Quad Cities Station consists primarily of 0 and 1+-
freshwater drum and gizzard shad (Commonwealth Edison Company, 1980, pp. 4-1 ;
- through 16).
166
Table 4: Impir.3ement Exploitation Rates (percent) at Quad Cities Station for cizzard Shad based on Estimated Standing Stocks for Slough-Lake liabitat in Pool 14 of the Mssissippi River during 1977 through 1979.
EstimateAl Standing Stock Impingement Exploitation Rate (Percent)b Estimated Weight Impinged (1b)
Total (Ib)a 1977 1978 1979 Data l'o/ Acre 50,276 27.767 2,494 Source 326.6 1 3P1,831 3.6 1.9 0.2 Ccmmonwealth Edison Co. (1980) 55.2 ~1 5,577 21.3 11.8 1.1 Muench (1978)
Christenson 39.9 170,281 29.5 16.3 1.5 g and Smith (1965)
C UMRCC(1947) 48.7 Savanna - 1 1.2 5,121 -- --
Savanna - 2 '.2. 4 52,919 95.0 52.5 5.2 L11RCC(1948) 0.7 c auawka - 1 81.2 346,531 14.5 8.0 1,742,075 2.9 1.6 0.1 Oguawka - 2 408.2 132 563,763 8.9 4.9 0.4 Average
- a. Total based on 4,267.7 acres slough-lake habitat in Pool 14
- b. Percentage calculated by dividing estimated weight impinged by the total estinacad standing stock f or slough-lake babitat
- # e
>+,2-o O.. OL /
' Table 5. Impingement Exploitation Rates (percent) at Quad Cities Station for Channel Catfish based on Estimated-Standing Stocks for. Slough-Lake Habitat in Pool 14 of the ,'
Mississippi River, 1977 through 1979. .
Estimated Standing Stock gingement Exploitatiem Rate (Percent)b Estimated Weight Impinged.(Ib)
Total (1b)a 1977 197g 1979 Data lb/ Acre 311 2,683 302 Source' 3.9 16,644 1.8 16.1. 1.8 Commonwealth
' Edison Co. (1980) ,
13.3 56,760 0.5 4.7 'O.5 Muench (1978) 119,069 0.3 2.2 0.3 Christenson 27.9 and Smith (1965) w
$ UlmCC . (1947) 69,137 0.4 'a 0.4 Savanna'- 1 16.2 22.8 9' 304 0.3 2.8 0.3 i Savanna - 2 t
UtmCC (194G)
Oquawka - 1 56.9 242,832 0.1 1.1 0.1 Oquawka - 2 11.4 48,65. 0.6 5.5 0.6 Average 26.7 114,051 0.3 2.4 0.3
- a. Total based on 4,267.7 acres for slough-Iske habicat in Pool 14.
- b. Percentage calculated by dividing estimated we.ght imeinged by i
the total estimated ctanding stock for slour;ir-lcke habitat.
Table 6. Impingement Exploitation Rates (percent) at Quad Cities Station for Bluegill Based on Estimated Standing Stocks for Slough-Lake !!abitat in Pool 14 of the Mississippi River, 1977 through 1979.
Estimated Standing Stock Impingement Exploitation Rate (Perceut)D Estimated Weight Impinged (Ib)
Data lb/ Acre Total (1b)a 1977 197g 1979 Source 182 158 139 Commonwealth Edison 3.2 13,657 1.3 1.1 1.0 Company (1980)
Muench (1978) 15.7 67,003 0.3 0.2 0.2 Christenson 8.0 34,142 0.5 0.5 0.4 and Smith (1965) g UMRCC (1947)
$ Savanna - 1 5.5 23,472 0.8 0.7 0.6 Savanna - 2 14.0 59,748 0.3 0.3 0.2 UMRCC (1948)
Oquawka - 1 5.8 24,753 0.7 0.6 0.6 Oquawka - 2 20.5 87,488 0.2 0.2 0.2 Average 10.4 44,323 0.4 0.4 0.3
- a. Total based on 4,267.7 acres for slough-lake habitat in Pool 14.
- b. Percentage calculated Ly dividing estimated weight impinged by the total estimated standing stock for the s'-2gh-lake habitat.
O O O
O O o Table 7. Impingement Exploitation Eates (percent) at Quad Cities Station for White Bass Based on Estimated Standing Stocks for Slough-Lake liabitat in Pool 14 of the Mississippi River, 1977 through 1979.
Impingement Exploitation Rate (Percent)b Estimated Standing Stock Estimated Weight Impinged (Ib) 1978 1979 Date Ib/ Acre Total (1b)a 1977_
1,155 122 600 Source 2.7 0.3 43,530 1.4 Commonwealth Edison 10.2 Company (1980) 5.2 10.0 1.1 2.7 11,523 Muench (1978) 9.4 18.0 1.9 1.5 6,402 Christenson and Smith (1965)
C LSIRCC (1947) 0.03 128 Savanna - 1 -
Savanna - 2 0.13 UMRCC (1948) 938 64.0 -
Oquawka - 1 J.22 11,949 5.0 9.7 1.0 Oguawka - 2 2.8 5.6 10.9 1.1 2.5 10,639 Average
- a. Total based on 4,267.7 acres for slough-lake habitat in Pool 14.
Percentage calculated by dividine estimated weight impinged by I
b.
the total estimated standing sto for slough-lake habftat.
Commercial Fish Harvest Commercial Iish harvest is discussed in Hazleton Environmental Sciences (1979 pp. 7.117 to 7.124) and in Commonwealth Edison Company (1980
- p. 3-49). In summary, commercial catcher during years of Station operation have been well within the range of commercial harvest records for the 27 years prior to Station operation, which indicates that Station operation has not affected commercial fishing.
Freshwater Drum Life History and Population Dynamics Study Of considerable importance to the 316(b) Demonstration is a freshwr.ter drum (Aplodinotus grunniens) life history and population dynanics study which was initiated in 1978 as part of the Quad Cities Station Aquatic Program. The species was selected on the advice of the Illinois Department of Conservation to receive special attention because all of its life history 9
stages are affected by Station operation, ar.d it is a sport and a major commercial species. Its eggs and larvae frequently constitute a majority of the condenser cooling water entrained ichthyoplankton. With the exception of gizzard shad (Dorosoma cepedianum), freshwater dra imtingement is numrically higher by a considerable margin than that for any othe species in Pool 14.
Thus, if it can be demonstrated that the combined ef fccts of entrainment and im-pingement do not result in a significant population decrease and a reducticn in the yield of freshwater drum to the commercial and sport fishery in Pool 14, it would be logical to assu=e that other species are probably not suffering adverse effects as a result of Quad Cities Station operation.
171
i Through 1979, freshwater drum larvae studies were directed at deriving estimates of entrainment survival and percentages of annual larvae drift lost to entrainment. Other studies were conducted to estimate population size, age class distribution, total annual mortality rates and impingement and commercial fishing annual exploitation rates. Larvae studies (Hazleton Environmental Sciences, 1979c) conducted in 1978 revealed that most larvae survive entrainment for open-cycle operation if discharge temperatures do not exceed 91,4*F. The percentage of larvae drift for each year lost due to entrain-ment for actual operating conditions was estimated, and ranged from 1.3 to 3.1 percent for the years 1975 through 1978, and from 1.6 to 5.4 percent for the samt years for the projected case of complete open-cycle operation. Studies conducted in 1979 (Commonwealth Edison Company, 1980) demonstrated that the estimates f or complete open-cycle were over-estimates. This was attributed to under-estimates of survival and over-estimates of entrainment abundance in the 1978 estimate. It is likely that there is not much difference in the number of larvae lost due to entrainment between open-cycle and the present operating modes.
In the spring of 1979, a mark-recapture population estimate for fish greater than 250 mm was made for a segment of Fool 14 (Commonwealth Edison Com-pany, 1980, pp. 5-1 through 5-25). The estimate was calculated based on the .
Chapman modification of the Schnabel multiple census estimate and its 95% con-fidence limit as deccribed by Ricker (1975). The point estimate was 189,845 fish v1th a 95% confidence interval of 117,553 to 398,060 fish. This estimate, which applies only to fish with a length greater than 250 mm, was considered to be applicable only to the portion of the freshwater drum population between O
172
RM 506.8 and RM 514.5, since recaptured fish were almost always taken near the original area of capture.
The population estimate study was expanded in 1980 to include mark and recovery areas downstream of the Station. In addition to the area sampled in 1979, the 1980 program included the area downstream of the Station between River Mile 495.0 and 506.0. The estimate for 1980 was 179,820 fish with a 95%
confidence interval of 96,586 to 368,784 fish (ERT, 1981) for fish of age class 4 and older. Age class four was the first age class to be fully recruited to the fishery.
Freshwater drum impingement exploitation rates for older fish in 1979 was estimated to be less than one percent (Commonwealth Tdison Company, 1980, p. 5-19). This estimate is based on fish marked and recovered from impingement collections in 1978 and 1979. As part of the 1978 fall haul seine program, 603 fish, 200 mm am larger were tagged and released. During the period December, 197G through 'Jecember, 1979, only two of the 1978 marked fish were found in impingement samplea. Secause approximately 40% of the total impingement vas sampled during this time period, the data suggescs an impingement exploitation rate of less than 1% (0.33) for fish greater than 200 cun.
Between April 16 and June 6,1979, there were 2178 fish greater than 250 mm, total length, tagged and released in the spring study area (Commonwealth Edison Company, 1980, p. 5-19). During the interval June, 1979 through June, 1980, only three fish marked in 1979 have been impinged. APFcoximately 40 percent of the total 1mpingement was again sampled during the same time period, which suggests that seven marked fish would have been impinged. For O
173
4 fish greater than 250 mm, the annual impingement exploitation would be O less than one percent (0.32%). This impingement exploitation estimate is only for larger fish and does not consider exploitation of small fish.
This low impingement estimate for largsr fish may be due in part to placement of the 3/4 inch bar mesh barrier net at the river's edge of the forebay. The net was in place from mid-December, 1978 through mid-April, 1979, and from the end of October, 1979 through the end of March, 1980. The net was in place during the period of the year when historically, larger drum had been collected in impingement samples. Consequently, it is not known what the impingement exploitation rate would have been had the net been out of the water.
The above impingement exploitation estimate is applicable only to older fish when the barrier net was in place and it would be inappropriate to use this estimate for exploitation of younger fish. Most impingement for this species is constituted by age class 0 and I, and a different approach was used to estimate exploitation for these younger fish. Two methods were used to estimate age class 0 and I abundances for the years 1973-1980 to be used to develop exploitation estimates for those years.
For the years 1973-1976, the reciprocal of the annual survival rate (0.561, ERT,1981) was multiplied by the estimated number of each fully re-cruited year class of a Pool 14 population estimate obtained in 1980, to obtain an estimate of the numbers of that year class in 1979. This procedure '
was followe'd for each preceding year for each year class until the number of each age class 0 and I of that year class was estimated. Results are pre-sented in Table 8.
174
1/
Table 8. Estimates for Age Class 0 and 1 Freshwater Drum from Backcalculation of 1980 Population Estimates.
~~~ Year 1975 1974 1973 1977 1976 Age Class 198QL/ 1979 1978 853,726 724,229 196,100 1,805,329 0 478,940 406,292 110,012 1,045,844 1 227,930 61,717 586,719 268,686 2
127,869 34,623 329,149 3
150,733 71,734 19,424 184,653 4 84,561 40,243 10,897 103,590 5
6 6,113 58,114 7 32,602 1/ Assumes constant survival rate of 0.561 between age classes 2/Basedon 179,820 Age 4-12 fish in 1980 which were fully recruited and vulnerable to hoop nets.
}
Source: ERT, 1981 Table 3-12 l
O O e
The second method was used to estimate the number of age 0 and 1 freshwater drum in the years 1977-80.. The estimates were obtained from a linear regre.esion (ERT,1981) which used age class as the independent variable anc' age class abundances in 1980 as the dependent variable. This procedure provides an estimate of the average number of age class 0 and I's estpected to be found in any year and is used to estimate impingement exploitation for recent year classes until that year class is fully recruited into the population estimate study.
Impingement exploitation ranges from 1.1 to 30.4 percent for age O fish and from 0.6 to 19.2 percent fcr age 1 fish (Table 9). These exploitation rates are, hewever, probably conservative or overestimates of impingement
' exploitation due to a variety of factors.
First, the exploitation rates were based on backcalculated population estimates that assumed a constant survival rate between age classes. This assumption is known to be invalid since survival rates-are lower for younger fish'. Second, the 1980 population estimate on which the backcalculations for year class 1973-1976 are based, is believed to be an underestimate. This underestimate was probably a result of inadequate sampling in certain (down-stream of the station) designated sampling-areas of the 1980 program (ERT, 1981). An underestimated population and overestimated survival rate would result in an overestimate of impingement' exploitation since both parameters-
-lead to smaller estimates of age class O_and I's. -This is particularly evident in the high exploitat1on rate estimated for age 0 (30.8%) and age 1 (19.2%).
freshwater drum fanpinged during 1974 and 1975 respectively (Table 9). It shouldLalso be noted that the age O fish in 1974 and age 1 fish in 1975 belong O
176
Table 9. Impingement Exploitation Estimates for Age Class 0 and 1 Freshwater Drum at Quad-Cities Station from 1973 through 1980.
Year 1977 1976 1975 1974 1973 1980 1979 1978 Age class O 724,229 196,100 1,864,250 estimatesl / 648,000 648,000 648,000 648,000 853,726 Estimated age clasa 0 60,373 118,849 28,540 24,453 8,928 impingement 2/ 6,827 11,048 23,380 Age class 0 impingement exploitat on 1.2 30.8 6.4 rate (%)1 1.1 1.7 3.6 4.4 /.9 Ageclass{/
estimate- 182,000 382,000 382,000 478,940 406,292 110,012 1,045,844 --
Estimated age class 1 21,160 48,287 19,688 impingementil 10,922 4,819 35.089 21,077 2,378
[
u Age class I impingement exploitation 19.2 4.6 -
2.9 9.2 4.4 0.6 rate (%)l/ 1.3 1/ Estimate based on population estimate of 179,820 Age 4-12 freshwater drum in 1980. Age O fish (1977-1980) and age 1 fish (1978-1980) were estimates of those age classes in any given year derived from linear regression (ERT, 1981).
2_/E stimated assumes all f reshwater drum impinged f rom July through December each year are age class O fish.
2/ Imptagement exploitation rate estimated by dividing age class impingement estimate by age class pope 1ation estLuate for each respective year.
4/ Estimate assumes all f reshwater drum impinged f rom January through June each year are age class I fish.
Sout E"T, 1981 Table 3-13 g
._ - _ _ . - - ._ _ _ _ = - . _ - - _ . . .
to the same year class. Estimated exploitation rates for other years (age 0 =-
(J 1.1 - 6.4% and age 1 = 0.6 - 9.2%) are lower than the above 1974 age 0 and 1975 age i estimates which further suggest that they are unrealistic.
Barrier Net Studies In 1979, the estimated impingement both for numbers and weights was the lowest recorded for the seven years of monitoring. This low estimate is
^ attributable to the placement of a barrier net in front of the forebay. The placement of the barrier net was initiated at the suggestion of the USEPA to evaluate its effectiveness in reducing impingement for the months during which impinsement has been shown to be greatest for closed-cycle or partial closed-cycle cooling. Results of the barrier net study during 1978-1979 indicated tnat impingement was reduced by 85 to 98% when the Station operated closed-cycle. A 48 to 78% reduction was measured during varying conditions of f( )
partial closed-cycle' operation (Commonwealth Edison Company, 1980,Section IV).
'It is expected, however, that this lower percentage for partially closed-cycle can be improved.
It is obvious from the results of the barrier net study that place-ment 1of this type of gear works fairly well during cloced-cycle operation at Quad Citfes Station. However, it-is also evident that the net could be effective in reducing impingement of river fish during open-cycle operation through the judicious operation of the circulating water pumps, and the return of condenser cooling water back to the forebay by means of the de-icing line, to reduce velocities at the river's edge of the forebay.
178
During the su=mer months, it is expected that impingement can be minimized during open-cycle cooling by returning condenser cooling water from the oischarge bay to the intake forebay via the icemelt line located on the floor of the forebay. The summer months have historically been the time when impingement of smaller individuals has been the greatest. Up to 200,000 gpm can be diverted back to the forebay through the icemelt line. By diverting condenser cooling water back to the forehay it ia expected that temperatures will increase enorgh in the forebay to cause smaller individuals to avoid the intake during this pericd of the year. The extent of the avoidance can only be documented through open-cycle operation.
During the winter months, impingenent can be minimized during open-cycle operation by installing the barrier net at the river's edge of the forebay in conjunction with reducing the number of circulating water poteps -
and by diverting condenser discharge back to the intake forebay by ueans h of the de-icing line. As mentioned earlier, larger sized fish have been impinged during closed-cycle operation for this period of the year b'cause of attraction to the intake forebay. During closed-cycle operation, the net has been shown to be effective in reducing impingement. Ly reducing the number of operating circulating water pumps, in addition to diverting con-denser discharge back to the forebay, intake velocities at the river's edge during open-cycle operation would correspondingly be reduced about 50% to about 0.5 fps. Low velocities in this area are necessary to ensure that the net rests on the floor or' the ferebay.
Finally, an added benefit to operating the Station in this manner is expected to be the absence of the thermal " leak" that occurs curing closed O
179
and. partial closed-cycle operation. It is expected that the absence of warm
-- water outside the forebay will result in reduced impingement. As mentioned
-.previously, this= warm water appeats to attract fich in the fall and winter.
A testing' period during open-cycle operation is the only method by which these hypotheses may be tested, but sufficient informatic: is already available to document that impingement would be reduced compared to open- v .e operation 1 1
i without the net or use of the de-icing line. The extent of the reduction cannot be quantified without operational data.
I
\
O O ,
O-180
Literature Cited O
Christenson, L.M. and L.L. Smith, 1965. Characteris' tics of Fish Populations in Upper Mississippi River Packwater Areas. U.S. Department of the Interior, Fish and Wildlife Service, Circular 212. Washington, D.C. 53 pp.
Commonwealth Edison Company, 1980. Quad Cities Aquatic Program, 1979 Annual Report. Chapters 1 through 5 and Appendices A, B, C, D and E.
Environmental Research and Technology, 1981. Freshwater Drum Life History and Population Dynamics Study in Quad Cities Aquatic Program - 1980 Annual Report. Chapters 1 through 4 and Appendices 4, B, C and b.
Hazleton Environmental Sciences, 1979c ironmen al Monitoring in the Missis-sippi River near Quad Cities St:t3 " gust, 1968 through December, 1978.
Chapters 1 through 8 and Appenoicea ., C and D.
, 1979b. The Survival of Entrained Ichthyoplankton at Quad Cities Station, June, 1978, RES No. 5501-05739. 55 pp.
, 1979c. Intensive Ichthyoplankton Studies at Quad Cities Station, June, 1978. RES No. 55105739. 339 pp.
Helms, D.R., 1968. Aquatic Habitat of the Mississippi River Bordering lova.
Iowa Quarterly Biology Reports. Vol. XX, No. 4, 11-14.
McFadden, J.T. , 1977. An Argument Supporting the Reality of Compensation in Fish Populations and a Plea to Let them Exercise It. In Proceedings of the Conference on Assessing the Effects of Power-Plant-Induced Mortality on Fish Populations. pp. 153-183.
Muench, B.A., 1978. Standing Crop Escinate for a Pool 14, M.ssicsippi River Backwater Area. Paper presented at the 16th Annual Meetin o of the Illinois Chapter, American Fishery Society. February 21-23, 1978.
NALCO Environmental Sciences,1977. Operational Environmental Monitoring in the Mississippi River near Quad Cities Station. February, 1976 through January, 1977. pp. 435-482.
Ricker, W.E., 1975. Computation and Interpretation of Biological Statistics of Fish Populations. Bulletin 191. Department of the Environment.
Fisheries and Marine Service, Ottawa,1975. 382 pp.
Upper Mississippi River Conservation Committee, 1947. An Experiment to Check Standing Crop in Two Backwate.. Ponds by the Use of Kotenone. In Pro-ceedings Third Annual Meeting. pp. 24-27.
1948. Poison C1nses of Mississippi River Backwaters near Oquawka, Illinois. In Proceedings Fourth Annual Meeting, pp. 18-25.
O 181
r,e,,r1 g
_ i _a! !u_ l ! J -. E f) v Literature Cited
]E ._Il f Christenson, L.M. and L.L. Smith, 1965.
Upper Mississippi River Backwater Areas.Characteris' tics of Fish Populations in Fish and Wildlife Service, Circular 212. U.S. Department of the Interior, Washington, D.C. 53 pp.
Commonwealth Report. Edison Company,1980. Quad Cities Aquatic Program, 1979 Annual Chapters 1 through 5 and Appendices A, B, C, D and E.
15 '" 1 Environmental Restarch and Technology, 1981.
- 2. ;
Freshwater Drum Life History and Fopulation Report. Dynamie s Study in Quad Cities Aquatic Program - 1980 Annual Chapters 1 through 4 and Appendices A, 3, C and D.
Razleton Environmental Sciences, 1979a.
sippi River near Quad Cities Station August, Environmental Monitoring in the M Chapters 1 through 8 and Appendices A, B, C and D.1968 through December, 1978.
, 1979b.
7- Station, June, 1978 The Survival of Entrained Ichthyoplankton at Quad Cities HIS No. 5501-05739. 55 pp.
, 1979c.
June, 1978. Intensive Ichthyoplankton Studies at Quad Cities Station, HES No. 55105739. 339 pp.
A
('}-
Helms, D.R., 1968.
Iowa Quarterly Aquatic Habitat of the tussissippi River Bordering Iowa.
Liology Reports.
, Vol. XX, No. 4, 11-14.
McFadden, J.T., 1977.
An Argument Supporting the Reality of Compensation in
__---- Fish Populations and a Plea to Let them Exercise It. In Proceedings of theFish on Conference on Assessing Populations. the Effects of Power-Plant-induced Mortality pp. 153-183.
Muench, B.A., 1978.
Backwater Area. Standing Crop Estimate for a Pool 14, Mississippi River Paper presented at the 16th Annual Meeting of the Illinois Chapter, American Fishery Society. February 21-23, 1978.
r-NALCO Environmental Sciences,1977.
- - - - in the Mississippi River near Quad Cities Station. Operational Environmental M February, 1976 through January,1977. pp. 435-482.
Ricker, W.E., 1975.
of Fish Populations.Computation and Interpretation of Biological Statistics Bulletin 191. Department of the Environment.
Fisheries and Marine Service, Ottawa,1975. 382 pp.
Upper Mississippi River Conservation Committee, 1947. An Experiment to Chcek
~
Standing Crop in Two Backwater Ponds by the Use of Rotenone. In Pro-
. - ~
ceedings Third Annual Meeting. pp. 24-27.
, 1948.
,- Oguawka, Illinois.
Poison Census of Micsissippi River Backwatcrs near
>) In Proceedings Fourth Annual Meeting, pp. 18-25.
<f r 181 w