ML20079N313

Fish Impingement Study, Tech Spec 2.2

ML20079N313
Person / Time
Site:	Fort Calhoun
Issue date:	11/11/1991
From:	King R OMAHA PUBLIC POWER DISTRICT
To:
References
RTR-NUREG-1437 AR, NUDOCS 9111110156
Download: ML20079N313 (46)

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Chapter 2 FISH IMPl!CEMDTI STUDY By Ronald G. King .

Technical Specification 2.2

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1. Introduction Fish impingement studies at Fort Calhoun Station have been conducted from May 1973 through December 1977. The studies were initiated to collect data necessary to evaluate the ef fects of 1 'ingement losses on the Missouri River fish community near the Station. The number, size, species, and physical condition of fish impinged on the traveling screens were determined. Daily samples were collected at noon (12 hr) and midnight (12 hr) from May through September and at noon only from October through April. A total of 2345 hourly samples was collected during the 56-month study, in addition, 24-hr impingement studies were conducted on 29 occasions from 1974 through 1976 to determine diurnal impingement rates. Impingement rates from the daily and 24-hr studica were evaluated to determine the best estimate of impingement rateo at Fort Calhoun S t a t ion. ,

11. Methods Fish were removed manually from the traveling screens for 60 nin following cleaning of the screens. During each hourly snmpling period, one of the six .

traveling screens was sampled on a rotational basis. All six screens were sampled during the 24-hr studies. Omaha Public Power District pertonnel collected the samples and compiled the data for the daily studies and the 1976 24-hr studies. The Ecosciences Division of Henningson, Durham & Richardson con-ducted the 24-hr studies in 1974 and 1975 (Henningson, Durham, & Richardson 1976),

111. Description of the Cooling Watet Intake Structure The Fort Calhoun Station intake is a reinforced concrete structure extending approximately 80 f t along the river bank at Fiver tule 645.85. Water is drawn into the intake by three 120,000 gpm capacity circulating water pumps. Water passes through a vertical trash rack with 3 inch openings prior to entet ing the six forebays. Water entering the plant must pass through the sluice gate openings located at the base of a curtain wall. Trash and debris which pass through the trash rack are removed by six traveling screens made of steel mesh with 3/8 inch square openings. A high pressure (110 psi) screen wach system is used to clean the screens. The screen wash trough discharges into the river et the downntream side of the intake structure.

IV. Results at.d Discussion A. Species Composition A total of 45 species was collected from the travelir.g screene at Fort Calhoun Station (1able 2.1). Species commonly impinged, in decreasing order of occurrence, includad freshwater drum (29.5%), gizzard shad (21.0%), channel catfish (9.0%), black bullhead (6.5%), white bass (6.2%), whitu crappie (4.4%),

and bluegill (3.6%). Combined, these species comprised 74 to 88% of the annual impingement and made up 80% of the fish sampled during the 56-month study.

Freshwater drum and gizzard shad were the most common species impinged throughout the study except in 1976 when channel catfish were the second most common fish collected (Table 2.1). Species that were occasionally common in the impingement collections (comprised more than 1% of the impinged fish) included carp, river 30

d carpsucker, stonecat, flathead catfish, green sunfish, yellow perch, and sauger.

Game fish (excluding freshwater drum) comprised from 25 to 62% of the annual impingement at the Station and averaged approxicately 39% over the entire study.

No rare and endangered species (Nebraska Game and parks Commission 1977) were impinged. Several species that were infrequently impinged, including mooneye, blacknose dace, highfin carpaucker, and black buf f alo, are listed as uncommon native fishes in Nebraska (Morris et al.1972) and as threatened species by Miller (1972). The silver jaw minnow was impinged in 1973; however, it apparently is not a native Nebraska fish (Horris et al.1972) and according to Cross (1967) probably does not occur naturally west of the Mississippi River.

B. 51re of Impinged Fish Fish impinged on the traveling screens at Fort Calhoun Station were generally less than 100 mm in length. During the 56-month study approximately 70% of the fish sampled were 100 mm or less. Fish longer than 100 en were impinged primarily from January through June. Nearly half of these larger fish were collected from November 1975 through May 1976. Based on published length data (Carlander 1969, 1977), few adult fish were impinged. Fish larger than 199 mm comprised only 2.7% of the fish sampled. Freshwater drum, shortnose gar, and gizzard shad accounted for approximately 60% of the fish that exceeded 199 mm in length. The small openings (3 inch) between the trash rack bars, the greater swinning ability of larger fish, and distribution of adult fish were the principal reasons why f ewer adult fish were impinged at Fort Calhoun Station. Electroshocking catch data collected near the Station indicated that fewer adult fish utilized the cutting bank habitat along the Nebraska shore when compared to the quiet water habitat behind the wing dikes along the Iowa shore (Chapter 1) . Adult individuals of small species, such as stonecat, centrachids, and black bul'1 heads were commonly impinged.

The average length of impinged fish decreased in Jcly (Figure 2.1) when young-of-the-year (YOY) fishes were large enough to be retained on the screens. Approximately 90% of the fish impinged between Jul; and December were YOY fish that were 100 mm or less in length. The lengths of impinged fish were variabic throughout tbe study; however, the monthly or annual average length of impinged fish seldom exceeded 140 mm (Figure 2.1). The average length exceeded 140 mm only when fewer than 10 individuals of each of the three most common species (freshwater drum, gizzard shad, and channel catfish) were sampled in a given month.

C. Physical Condition of Impinged Fish Fish campled from the traveling screens were classified as airher alive or dead. The physical condition of impinged fish was variable ranging from 0 to 90% dead on a monthly bacis (Figure 2.2). Survival was lowest when water temperatures were high (July through August) or when most of the fish impinged were gizzard shad or freshwater drum. The highest survival occurred at low water temperatures or when most of the impinged fish were ictalurids.

The percentage of dead fish generally increased in July and remained high into early winter. During this period YOY fishes dominated the samples and the average length of impinged fish decreased (Figure 2.1) . Only 25% of fish larger than 199 mm were recorded as dead, while 60% of the fish larger than 299 mm were dead. Larger fish may have been stressed prior to being entrapped 31

c-h in the for.* bay area. The length of time that fish are entrapped in the intake o lucture s> fore being impinged is an important factor in determining the

'ysical condition of fish sampled f rom the screens. The physical condition of fish in the intake may progressively deteriorate with tico.

Approximately 50% of the fish sampled were recorded as dead during the study. The annual percentage classified as dead ranged from 30.7% in 1976 to 73.4% in 1974 Similar trendh among years were also noted at Cooper Nucicar Station, approximately 113 miles downstream of Fort Calhoun Station (King 1978).

The low percentage of dead fish in 1976 was attributed to a reduction in number of gizzard shad and freshwater drum in the impingement collections and a higher survival of these species. During all other years 95% of the dead fish were gizzard shad and freshwater drum, compared to 27% in 1976. Of the major species impinged (Table 2.2), gizzard shad had the lowest percent of individuals classified as alive (28.3%), followed by f reshwater drum (38.2%),

bluegill (50.6%), white bass (51.3%), white crappie (53.6%), channel catfish (71.8%), and black bullhead (80.9%). The survival rate of impinged fish classified as alive af ter being returned to the river is not known. Therefore, because of the varying degrees of physical damage reported by Henningson, Durham and Richardson (1976) and the high pressure screen wash,100% of the impinged fish were assumed lost from the fish community.

D. Impingement Rates Daily impingement rates (no. fish /hr per screen) were highly variable, ranging from 0 to 71 fish /hr per screen (Figure 2.3). No fish were impinged during approximately 57% of the daily sampling periods. Impingement rates were generally less than 10 fish /hr per screen with higher rates recorded on only 68 dates during the 56-month study (Figure 2.3). High impingement rates (110 fish /hr per screen) were generally associated with impingement of f resh-watet drum and gizzard shad. Gizzard shad comprised all but three of the fish sampled on 13 July 1975, when the highest impingement rate was recorted (71 fish /hr per screen). Other species that dominated the samples when impingement rates exceeded 10 fish /hr per screen included channel catfish, black bullhead, white bass, green sunfish, and white crappie.

Year-to-year variability in impingement rates was attributed to several factors. High impingement rates in the winter are related to reduced swimming ability of fish in cold water and the higher approach velocities at the intake structure associated with reduced river flows. Fish activity also may increase as the river flow decreases since fish must seek vintering areas as the backwater areas are devatered. Although there appears to be a general relationship between impingement rates and river flow, it was not always evident. For example, the lowest approach velocities occurred in 1975 during the high summer flows (Figure 2.4), yet the lowest summer impingement rates occurred in 1976 when river flows were substantially lower. Impingement rates are probably related more to fish movements and abundance of YOY fish than strictly to flow conditions.

The highest impingement rates occurred f rom December 1975 through May 1976. The impingement rate remained high during this period; however, in other years the rates decreased in the winter and early spring (Figure 2.3).

Fish collected from the traveling screens from December 1975 through May 1976 32

accounted for approximately 30% of the fish sampled during the entire study, and the number sampled was 5-9 times greater than during other comparable periods.

impingement rates increased significantly on 4 December 1975 (Figure 2.3) following a rapid decrease in river discharge (Figure 2.4). Reduced flows probably caused fish to disperse from the previously inundated shoreline and backwater areas.

Based on size data, these high impingement rates indicate a greater abundance of YOY and yearling fish in 1975-76 than in other years. The high river flows from Jul.y through November 1975 may have created larger nursery areas f or YOY fish which may have resulted in the increase in YOY fish. Increased recruitment of YOY fish may also have resulted from the high discharges from Lewis and Clark Lake, since Walburg (1971) reported that large numbers of YOY fishes are discharged through Cavius Point Dam.

Size is also an important f actor contributing to variability in im-pingement rates. The highest impingement rate occurred on 13 July 1975 when the average length of impinged fish was less than 60 mm. Impingement rates generally decreased when the average-size of the impinged fish increased. Swimming speeds of fish are directly related to body size and water temperature (Bainbridge 1958). At the water temperatures reported at Fort Calhoun Station the sustained swimming speeds of most smaller fish are slower than the approach velocities through the sluice gaten (Henningson, Durham and Richardson 1976).

It is apparent that several interrelated factors affect impingement rates at Fort Calheun Station. Natural variability in water temperature, spavning and recruitment success, seasonal distribution and abundance of fishes, and controlled river flows all apparent)v affect impingement at Fort Calhoun Station.

Impingerent rates at Fort Calhoun Station exhibited diel dif ferences (Figure 2.5) based on the 22 24-hr studies conoucted in 1974 and 1975 (Henningson, Durham and Richardson 1976). Impingement rates at night (2000 to 2200, and 0200 to 0400 hr) were significantly (p 10.05) higher than during midday (1400 to 1600 hr). Seven additional 24-hr studies during 1976 indicated a similar trend (Figure 2.5). The number of fish impinged during the summer montha in 1976 (<50/24-hr) was too low to establish diel differences. The daily samples collected hourly at noon and midnight generally did not exhibit these dif ferences (Table 2.3). The lack of diel differences in the hourly studies was probably related to the scheduled sampling periods. The impingement rates at Cooper Nuclear Station, where samples were collected at random times, were generally higher at night (King 1978). There were no apparent diel differences in the impingemont rates of the major species (Table 2.6).

Diel differences in impingement rates have been attributed to increased fish activity from early evening through the morning houta, decreased visibility of the traveling screens at nicht and the physical condition of impinged fish (Landry and Strawn 1974L Hyman et al.1975; Marcy 1975). Landry and Strawn (1974) reported increased catch rates at night when poor visibility of the traveling screens probably decreased screen avoidance, while during daylight hours, injury rates were high, suggesting that fish in a weakened condition could not avoid the screens. Large differences between day and night in the percentage of alive impinged fish at Fort Calhoun Station occurred in 1975 l (Table 2.4). In 1975, 24% of the fish sampled during the day were alive 1

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compared to 46% st night. These differences, however, did not result in diff erent impingement rates when day and night samples were compared (Table 2.3).

Data from the 24-hr sud hourly impingement studies were compared to determlne the reliability of using daily impingement rates to project the total number c( fish impinged at Fort Calhoun Station. Hourly samples overestimated daily impingement rates on 14 of 29 occasions and underestimated daily impinge-ment rates on 12 dates when comparable 24-hr data were available (Table 2.5).

High iuringement rates, which occurred over a few days, were f requently missed by the 24-hr sac 21es which were conducted monthly or biveekly. For example, the high inningement rates which occurred over a 6-day petiod in July 1975 (Tigore 2.3) were not detected by the 24-hr studies conducted on 5-9 and 22-23 July 1975 (' able 2.5). The daily samples were most likely to underestimate impingement tates when fish appeared sporadically on the screens (Figure 2.1).

, Despite these differences, the daily impingement values based on the number of fish /hr per screen were not significantly (p > 0.05) different from the 24-hr studies when compared using the paired "t" statistic (t = 1.56, d.f. = 28). The impingement rates for each of the six screens were compared to determine if a certain screen or screens biased the monthly impingement raten. Even though .

considerable variation in impingement rates occurred among screens (Table 2.7),

no statistical differences (p > 0.05) were evident. The 24-hr studies also indicated that the differences in impingenent rates among screens were not significant (Henningson, Durham & Richardssn 1976). Based on these comparisons, the daily samples provide an accurate estitate of the monthly impingement rates.

Projected monthly impingement ranged from 288 fish in February 1975 to 42768 fish in March 1976 (Table 2.8). An estimated 492,040 fish were impinged at Fort Calhoun Station from Ma) 1973 through December 1977.

E. Impact Commercial catch data from the Miscouri River between Sioux City. Iowa, and the Platte River indicate no decline in tbe fishery following Station start-up in 1973 (Table 2.9) . The catch per piece of fishing gear increased from 3.8 fish in 1974 to 6.8 and 6.1 fish in 1975 and 1976, respectively. The catch of carp, buffalo, and suckero has lacreased f rom 1974 through 1976, whereas the catch o+ channel cattish has declined since 1974 (Table 2.9). The catch per piece of fishing gear for channel catfish decreased from 1.5 in 1974 and 1975 to 1.0 ' sh in 1976.

The impact of the removal of nearly 500,000 fish f rom the Missouri River can be put into perspective by comparing the number impinged with available harvest data. Commercial catch data from the Missouri River were compared to the number of important commercial species impinged at Fort Calhoun Station (Table 2.9). Because most of the fish impinged were YOY or yearling fish, all of these fish would not have survived to harvestable size. Hesse and Wallace (1976) determined the annual mortality rates for five commercial species in the Kissouri River. Using these data, the number of impinged fish that may have reached harvestable size, had they not been impinged, can be estimated (Table 2.9).

These estimates are conservative since mortality rates of age class 0 fish were not determined, except f or bigmouth buf f alo. The potential number of harver. table fish removed by impingement was lov, except in 1976 when a high number of ch.nnel 34

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catfish was 16 pinged (Table 2.9). Since commercial species in the Missouri River are generally 3-4 years old before they reach a harvestable size (llesse and Wallace 1976: Schainost 1976), the impact of impingenent losses would not af f ect the commercial catch until 1976 and 1977. The 1977 commercial catch data art unavailable at this time. The decreased catch of channel catfish in 1976 was probably related to factors other than impingement, since the impingement rates of channel catfish were lov in 1973 and 1974. Schainost (1976) suggested that the general decline in the Missouri River commercial fishery may be due to a change in the type of fisherman. Evid.:ntly commercial fishing on the tussouri River is becoming more of a hobby than a livelihood.

Mortality rates of the two most common species ispinged (gizzard shad and freshwater drum) have not been determined in the Missouri River.

Survival of gizzard shad from egg to adult is probably lesp than 1% based on the high mortality reported for other clupeide (Kissil 1974 Leggett 1977).

Assuming a survival rate of 0.1 to 1.0%, approximately 104-1050 of the gizzard shad impinged would have survived to maturity. Comparative data f or freshwater drum are unavailable, but assuming a natural mortality of 90%, an estimated 14515 f reshwater drum would have survived to maturity.

A comparison of catch and relative abundance data f rom 1972-73 surveys in the channelized Missouri River (Gould and Schmulbach 1973; Stucky 1972) with data collected since 1973 near Fort Calhoun Station and Cooper Nuclear Station (Hesse and Wallace 1976: Bliss 1978a) and near the Nebraska City Power Station (Bliss 1978b) indicates no significant changes in the fish populations in the tussouri River.

Losses of fish due to ispingement on the traveling screens has had no detectable ef fect on fish populations in the vicinity of Fort Calhoun Station.

Standing crop estimates necessary to make a direct assessment of impact are not available. However, based on catch and size data, changes in the fish community have not been noted (Chapter 1). The numerical catch near the Station varied substantially among years but species relative abundance was similar from 1973 through 1977. The dif ferences in numbers of fish collected were related to an ettraction or avoidance of fish to the varm water and subsequent alteration of their dictribution. In addition, river conditions caused variations in catch rates, erpecially in 1975, when unusually high flows occurred. The average size of fish was quite uniform among years, indicating fish stocks have not been reduced.

Fish losses attributed to impingement may be off set by the natural ,

compensatory capacity of fish populations which tends to cause a decrease in death rate or increase in birth rate as population density declines (McFadden 1977). Since the fish impinged at Fort Calhoun Station are small, immature fish, the potential impact on the fich populations in the Missouri River is probably low. If these fish are removed when natural mortality is still compensatory, the removal may be of f set by increased survival and/or growth (Ricker 1954) .

V. Summary and Conclusions

1. Species commonly impinged included freshwater drum, gizzard shad, channel catfish, black bullhead, white bass, white crappie, end bluegill.

Combined, these species comprised 74 to 88% of the annual total of impinged fish at Fort Calhoun Station.

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2. No rare or endangered species were impinged. l l

3. During the 56-month it.udy approximately 70% of the fish sampled were l 100 mm rr less in length. Fish longer than 199 mm comprised only 2.7% of the fish sampled.

4. Approximately 50% of the fish sampled were recorded as dead during the study. Survival was related to water temperatures and the size and species of fish impinged. The number of dead fish was highest when YOY gizzard shad and f reshwater drum were thundant.

5. Daily impingement rates ranged from 0 to 71 fish /hr per screen. High impingement rates were generally associated with impingement of gizzard shad and freshwater drum.

6. Variations in impingement rates were related to natural variability in water temperature, spawning and recruitment success, seasonal distribution and abundance of fishes, and controlled river flows.

7. A comparison of hourly and 24-hr studies indicated that the daily studies provided, an accurate estimate of the monthly impingement rates.

8. Projected monthly impingement ranged from 288 to 42768 fish an estimated 492,040 fish were impinged a. Fort Calhoun Station from May 1973 through December 1977.

9. Impingement loesen were assumed to be 100%, although e ame survival may have occurred since approxtaately 50% of the fish sampled were classified as alive and vore returned to the river.

10. A comparison of catch and size data since Station start-up indicates that impingement losses has had little impact of the Missouri River finh community in the vicinity of the Station. ,

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VI. References Cited ,

Bainbridge, R. 1958. The speed of swimming of fish as related to size and to the frequency and amplitude of the tailbeat. J. Expl. Biol. 35:104-133.

Bliss, Q. P. 1978a. Fish population and distribution study. Pages 147-179 in The evaluation of thermal effects in the Missourt River near Cooper Nuclear Station (Operational Phase), January-December 1977. (Project No. 5501-08776). Report prepared by NALCO Environmental Sciences for Nebraska Public Power District, Columbus, Nebr.

. 1978b. Estimation of fish population in the Missouri River near the Nebraska City Power Station, November 1977. (Project No.

5501-08880). Report pre:4 red by NALCO Environmental Sciences for Omaha Public Power District, Omaha, Nebr.

Carlander, K. D. 1969. Raelbook of freshvater fishery biology. Vol. 1.

Iowa State University Press Ames, Is.. 752 pp.

. 1977. Handbook of freshwater fiahery biology. Vol. 2. Iowa State University Press, Ames, la. 431 pp.

Cross, F. B. 1967. Handbook of fishes c. ' . mas. Univ. Kans. Hus. Nat.

Eist. Misc. Publ. No. 45. 357 pr.

Gould , C. , and J. C. Schmulbach. 1973. Relative abundance and distribution of fishes in th( Missouri River, Gavine Point Dam to Rulo. Nebraska.

Final Rep. Missouri River Environ. Inventory. U. S. Army Corps of Engineers Omaha, Nebr. 60 pp.

Henningson, Durham. & Richardson, 1976. Analysis of impingement at Fort Calhoun Station. Supplement No. I to the Fort Calhoun Unit No. 2 Environ-mental Renort, Report prepared f or Omaha Public Power District Omaha, Nebr. 35 pp.

Hesse L. W. , and C. R. Wallace. 1976. The effects of cooling water discharges f rom Fort Calhoun and Cooper Nuclear Stations on the fishes of the Missouri River. Nebr. Game and Parks Comm. , Lincoln, Nebr. 378 pp.

Hyman, H. A. H. , W. H. Howbray, and S. B. Sa11a. 1975. The effects of two electrical barriers on the entrainment of fish at a freshwater nuclear power plant. Pages 205-237 in 8. B. Saila, ed. Fisheries and energy productions a symposium. D. C. Heath and Co., Lexington, Mass.

King , R. G . 1978. Fish impingement and entrapment. Pages 180-195 in The evaluation of thermal effects in the Missouri River near Cooper Nucicar i Station (Operational Phase), January-December 1977. (Project No. 5501-08776),

Report prepared by NALCO Environmental Sciences for Nebraska Public Power District, Columbus, Nebr.

l Kissil, G. W. 1974. Spawning of the anadromous alewife, Alosa pseudoharengus in Bride Lake, Connecticut. Trans. Am. Fish. Soc. 103(2):312-317.

l 37

. . . . + . - - e m.-,-.,. ,, - , . . .- ,,,.-,....,.._mm..,,._..m.., ,..m._, m... . . _ . _ . , _ . _ _ . . _ . . ._....m,.,- -

Landry , A. M. , Jr. , and K Gtrawn. 1974. Number of individuals and injury

• rates of fishes caught on revolving screens at the ?. H. Robinson Generating Station. Pages 263-271 in L. D. Jensen, ed. Proceedings of the second entrainment and in6ske screening workshop. Johns Hopkins Univ. Rep. No,

15. Electric Power Res. Inst. , Palo Alto, Calif.

Leggett, W. C. 19 ,* 7 . Density dependence, density independence, and recruitment in the Amnrican shad (Alosa sapidissima) population of the Connecticut River. Pages 3-17 in W. Van Winkle, ed. Proceedings of the conference on assessing the ef f ects of power-plant induced mortality on fish populations.

Pergamon Press, New York.

Marcy, B. C. , Jr. 1975. Entrainment of organisms at power plants, with emphasis oc fishes - ma ev arview. Pages89-106! !g S. B. Saila, ed.

Fisherica and energy pru.*n rions a symposium. D. c. Heath and Co.,

Lexington, Mass.

McFadden, J. T. 1977. An argument supporting the reality of compensation in fish populations and a plea to let them exercise it. Pages 153-183 in W. Van Winkle, ed. Proceedings of the conference on assessing the effects of power-plant induced mortality on fish populations. Pergamon Press, New York. -

Miller, R. R. 1972. Threatened freshwater fishes of the United States.

Trrns. Am. Fish. Soc. 101(2):239-252.

Morris, J., L. Morrie, and L. Witt. 1974. The fishes of Nebraska. Nebr.

Cate and Parks Comm. D. J. Rep. , Proj . F-4-R. 98 pp.

Nebraska Game and Parks Commission. 1977. Nebraska's endangered and thre.itened wildlif e. Nebr. Game And Parks Comm., Lincoln, Nebr. 35 pp.

Schainost, S. 1975. Jurvey of 1974 commercial fisheries industry of Nebraska. _

Proj ect No. 2-223-R. Nebr. Game and Parks Cumm., Lincoln, Nesr. 42 pp.

. 1976. Survey of 1975 commercial fisheries industry in Nebraska.

Project No. 2-223-R. Nebr. Game and Parks Comm. , Lincoln, Nebr . 40 pp.

,. 1977. Survey of 1976 commercial fisheries indut . ry of Nebraska.

Proj ect No. 2-214-R. Nebr. Game and Parkt Comm.. Lincoln, b ,br. 31 pp.

SturJ:y , :.4 P. 1972. Selected environmental ef fects cf two nuclear power riants on the Missouri River. Preoperational Progress Report. Nebr.

t Game and Parks Comm., Lincoln, Nebr. pp. 1-18.

Ricker, W. E. 1954. Stock and recruitment. J. Fish. Res. Board Can. 11:5 9-623.

Walburg, C. H. 1971. Loss of young fish in reservoir discharge and year-class survival, Lewis and Clark Leke, Missouri River. Pages 441-448 ja G. E.

Hril, ed. Reservoir fisheries and limnology. Am. Pish. Soc. Spec. Publ.

No. 8.

38

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' table 2.1. Sunsr.ary of the number and relative abundance (%) of fish collected from the traveling screens at Fort Calhoun Station ner.r the Missouri '

River, 1973-77.

1973 _ 1974 1975 1976 1977 >

$pecies No. 2 ho. ho.

I 1 Wo. I ho. 1 7otal Percent Sh;velnose sturgeos =0 0.0 1 0.1 0 0.0 0 n.0 0 0.0 1 <0.1 Longnose ser 0 0.0 0 0.0 0 0.0 1 0.1 0 0.0 1 <0.1 Shcrtnoes 5ar 0 0.0 10 1.0 3 0.4 4 0.3 0 0.0 17 0.4

.American eel- 1 0.1 0 0.0 0 0.0 0 0.0 0 ; 0.0 1 <0.1 Skipjeck horrins 0 0.0 2 0.2 0 0.0 0 0.0 0 '0.0 2 <0.1 Cissard shed 170 19.7 275 27.4 312 39.3 94 7.8 68 14.2 919 21.1 Mooneye 0 0.0 2 0.2 0 0.0 0 0.0 0 0.0 2 <0.1 Goldeye 0 0.0 1 0.1 1 0.1 2 0.2 4 0.8 8 <0.2 Northern pike 1 0.1 - 0 0.0 0 0.0 2 0.2 0 0.0 3 <0.1 hekellunge 1 0.1 -0 0.0 0 0.0 0 0.0 0 0.0 1 <0.1 Cyprinidas 1 0.1 0 0.0 0 0.0 1 0.1 1 0.2 3 <0.1

--Carp 26 3.1 16 1.6 17 2.1 21 1.7 5 1.0 85 2.0

-81 cknose. dace 1 0.1 0 0.0 0 0.0 0 0.0 0 0.0 1 <0.1 Silvery minnow 2 0.2 0 0.0 0 0.0 0 0.0 0 0.0 2 <0.1

- Silver jaw minnow -_ 1 0.1 0 0.0 0 0.0 0 0.0 0 0.0 1 <0.1

' Silver chub 0 0.0 0 0.0 1 0.1 2 0.1 1 0.0 4 <0.1 Emerald shiner 0 0. 0 - 0 0.0 0 0.0 1 0.1 0 0.0 1 <0.1 Red shiner 0 0.0 0 0.0 2 0.3 0 0.0 0 0.0 2 <0.1 *

.F:thead minnov- 0 0.0 0 0.0 1 0.1 0 0.0 0 0.0 1 <0.1 creek chub ~ 0 0.0 1 ' O.1 0 0.0 1 0.1 1 0.2 3 <0.1 River carpeucker 18 2.1 10 1.0 7 0.9 11 09 12 2.5 58 1.3

- Mishfin carpencher 5 0.6 18 1.8 0 0.0 2 0.2 0 0.0 25 0.6 White sucker - 1 0.1 1 0.1 0 0.0 0 0.0 0 0.0 2 <0.1 Blue sucker 1 0.1 5 0.5 2 0.3 10 0.8 3 0.6 21 0.5 Smallmouth bufIaio 0- 0.0 1 0.1 4 0.5 26 2.2 1- 0.2 32 0.7

'Biguouth buffalo. 0 0.0 3 0.3 9 1.1 7 0.6 2 . 0.4 21 0.5

- Bitek buffalo 0 0.0 0_ 0.0 20 2.5 0 0.0 0 0.0 20 0.5 Shsrthead redhorse -I 0.1 0 0.0 0 0.0 14 1.2 3 0.6 18 0.4

. 31rck butlhead - 52 6.0 87 8.6 43 5.4 92 7.6 9 1.9 283 6.5 tallow bullhead 1 0.1 2 0.2- 0 0.0 0 0.0 0 0.0 3 <0.1 Channel catfish 36 4.2 26 2.6 69 8.7 203 16.8 56 11.7 390 9.0

'Stineest 0 0.0 1 0.1 30 3.8 32 2.6. 7 1.5 70 1.6

-T1:thead catfish -23 2.7 9 0.8 21 2.6 17 1.4 11 2.3 81 1.9 turbot 2 0.2 3 0.3 0 0.0 l' O.1 0 0.0 6 0.1

- White base s 51 5.9 31 5.1 22 2.8 122 10.1 25 5.2 271 6.2 Green eunfish 56 6.5 2 0.2 36 4.5 13 1.1 6 1.3 113 2.6 Or nsespotted sunfish 2 C.2 0 0.0 4 0.5 3 0.2 .0 0.0 9 0.2

'Loogear sunfish 1 0.1 0 0.0 0 ' O.0 0 0.0 0 0.0 1 <0.1

- Blues 111 10 1.2 19 1.9 41 5.2 80 6.6 8 1.7 158 3.6 Larsemouth base 0 0.0 0 0.0 0 0.0 11 0.9 1 0.2 12 0.3 White crapple 25 2.9 36 3.6 24 3.0 94 7.8 13 2.7 192 4.4-11tek croppie - 5 0.6 4 0.4 2 0.3 4 0.3 0 0.0 15 0.3 iYallow perch 2 0.2 0 0.0 5 0.6 35 4.5 0 0.0 62 1.4

$1 user- 1 0.1 0 0.0 4 0.5 51 4.2 6 1.3 62 1.4 Walleye 4 0.5 12 1.2 3- 0.4 6 0.5 2 0.4 27 0.6 Freshwater drum- 362- 41.8 394 39.2 85 10.7 209 17 3 234 48.8 1284 29.5 Unidentified fish 2 0.2 14 1.4 25 3.2 17 1.4 0 0.0 58 1.3 Tats 1- 865 1006 793 1209 479 4352 e

44

,e- e , , - , , . - , ~n ,, , -, e

Table 2.2. Summary of the physical condition of major spectee impinged at Fort Calhoun Ststion. 1973-77.

-Number ,

Species Alive Dead Total Percent Alive Shortnose gar 9 8 17 52.9 Gizzard shad 260 659 919 28.3 Carp 62 23 85 72.9 River corpsucker 30 28 56 51.7 111ghfin carps. icker 10 15 25 40.0 Blue sucker . 13 8 21 61.9 Bismouth buf f alo 14 7 21 66.7 Black buffalo 20 0 20 100.0 Shorthead redhorse 13 5 18 77.2 Black bullhead 229 54 283 80.9 Channel catfish 280 110 390 71.8 Stonecat 51 19 70 72.9 Flathead catfish 36 45 81 44.4 White bass 139 132 271 51.3 Green sunfish 77 36 113 68.1 Bluegill 80 78 158 50.6 White crappie 103 89 192 53.6 Yellow perch 50 12 62 80.6 Sauger 42 20 62 67.7 Walleye 22 5 27 81.5 Freshwater drum 490 794 1284 38.2 Total 2030 2147 4177 48.6 45 i

i Table 2.3. Number of fish impinged per hour and average size of fish impinged during diurnal and nocturnal sampling periods in May-September 1973-77 at Fort Calhoun Station.

(Diurnal (1200 hr) Nocturnal (2400 hr)

Sample No. Avg Size Sample No. Avg Size Month Periods Fish Avg /Hr (mm) Periods Fish Avg /Hr (mm)

May 1973 5 49 9.8 84 June 1973 11 7 0.6 89 30 68 2.3 88 30 15 0.5 70 July 1973 31 80 2.6 81 August 1973 32 60 1.9 60 30 80 2.7 62 35 191 5.5 56 September 1973 30 21 0.7 67 30 79 2.6 61 Total 126 298 2.4 138 352 2.6 May 1974 31 33 1.1 155 June 1974 31 60 1.9 134 30 48 1.6 131 30 11 0.4 113 i July 1974 32 27 0.8 43 August 1974 31 48 1.5 87 31 63 2.0 70 31 52 1.7 90 September 1974 29 51 1.8 73 30 72 2.4 75 Total 153 222 1.5 153 243 1.6 May 1975 31 14 0.5 103 31 37 1.2 103 June 1975 30 20 0.7 59 29 24 July 1975 0.8 53 31 1 34 4.3 56 30 131 4.4 57 August 1975 31 11 0.4 50 September 1975 30 4 0.1 111 30 8 0.3 67 30 1 <0.1 185 Total 153 187 1.2 150 197 1.3 May 1976 30 150 5.0 105 June 1976 29 80 2.8 105 30 50 1.7 95 30 33 1.1 123 July 1976 31 10 0.3 93 August 1976 31 4 0.1 107 31 7 0.2 78 31 0 0.0 0 September 1976 30 3 0.1 166 30 1 <0.1 85 Total 152 220 1.4 151 110 0.8 May 1977 31 18 0.6 258 June 1977 31 4 0.1 129 30 16 0.5 201 30 0 0.0 0 July 1977 31 48 1.5 68 August 1977 31 1 <0.1 285 30 50 1.7 68 31 3 0.1 139 September 1977 30 52 1.1 68 30 16 0.5 102 Total 152 164 1.1 153 _24 0.2 46

e m eJ -

Table 2.4. Summary of the physical condition of fish impinged during day and night sampling l

periods at Fort Calhoun Station, 1974-77.

l l

l 1974 May-September 1975 May-September l

Day Night Day Night Species Live Dead % Live Live Dead % Live Live Dead % Live Live Dead % Live l

9.2 108 4.4 11 104 9.6 29 82 26.1 Gizzard shad 9 98 5 62.5 l Carp 4 3 57.1 5 4 55.6 1 3 25.0 5 3 36 7 83.7 13 9 66.7 2 4 33.3 13 3 81.2 f Black bullhead 0 100.0 1 7 12.5 9 3 75.0 l Channel catfish 0 2 0.0 2 82.4 Stonecat 0 0 0.0 0 0 0.0 3 4 42.9 14 3 0 0 0.0 0 1 0.0 0 1 0.0

) Flathead catfish 0 4 0.0 0

0 1 0.0 2 3 40.0 0 0 0.0 0 0.0 Miite bass 0 0 0 0.0 6 0 100.0 0 0 0.0 Green sunfish 0 0.0 Bluegill 2 2 50.0 9 1 90.0 9 6 60.0 0 0 0.0 l l

62.4 3 25.0 0 4 0.0 l l White crappie 5 6 45.5 14 3 1 0 0 0.0 0 0 0.0 0 0 0.0 0 0 0.0 l O Yellow perch 0 0 0.0 0 0 0.0 0 0 0.0 0 0 0.0 j Sauger 22 18.5 10 32 23.8 2 5 28.6 2 0 100.0 i Freshwater drum 5 13 18.7 8 10 44.4 9 5 69.2 8 8 50.0 l Other 3 Total 64 158 28.8 73 170 30.0 45 142 24.1 90 107 45.7 l

l l

Table 2. rs . (continued) 1976 May-September 1977 M:ay-September Day Night Day Night Species Live Dead % Live Live -Dead % Live Live Dead % Live Live- Dead % Live Girzard shad 10 8 55.6 1 3' 25.0 16 9 64.0 0 2 0.0 Carp ,

2 0 100.0 3 1 75.0 0 1 0.0 0 1 0.0 Black bullhead 4 0 100.0 13 3 81.2 2 3 40.0 0 1 0.0 Channel catfish 30 13 69.8 14 4 77.8 1 0 100.0 0 0 0.0 Stonecat 8 3 72.7 5 1 83.3 2 2 50.0 0 0 0.0 Flathead catfish 2 0 100.0 4 1 80.0 2 4 33.3 0 1 0.0 White bass 13 8 61.9 4 3 57.1 4 6 40.0 1 0 100.0

' Green sunfish 2 0 100.0 1 1 50.0 2 2 50.0 0 1 0.0 Bluegill 13 2 86.7 10 1 90.9 2 3 40.0 0 0 0.0 White crappie 25 7 78.1 7 5 58.3 4 2 66.7 0 0 0.0 Yellow perch 5 0 100.0 3 0 100.0 0 0 0.C 0 0 0.0 Sauger 4 0 100.0 2 1 66.7 2 1 66.7 0 0 0.0

$ Freshwater drum 21 22 48.8 10 5 66.7 32 53 37.6 2 9 13.2 Other 16 2 88.9 10 2 83.3 6 3 66.7 1 5 16.7 Total 155 65 70.5 87 31 73.7 75 89 45.7 4 20 16.7 I

i i

I

.- . 1

Table 2.5. Summary of daily impingement rates (no, fish / day) based on 24-hr and daily studies at Fort Calhoun Station, 1974-76.

I No. Fish Impinged / Day Date 24-hr Daily Hourly S-6 September 1974 274 418 5-6 November 1856 4320 12-13 November 566 576 18-19 November 661 216 20-21 January 1975 50 72 19-20 February 5 72 31-22 April 154 216 6-7 May 137 216 27-28 May 36 0 10-11 June 55 0 23-24 June 372 144 8-9 July 239 0 32-23 July 174 72 5-6 August 59 144 20-21 August 79 72 4-5 September 48 144 17-18 September 71 72 5-6 October 84 0 21-22 October 149 0 4-5 November 252 216 1B-19 November 304 504 2-0 December 49 936 25-26 March 1976 797 1152 23 24 April 324 288 28-29 May 463 1800 16-19 June

~

207 72 16-17 July- 42 288 13 August 15 0 17 September 14 144 49

a g

' Table 2.6. Summary of the ntunber of major species sampled during diurnal and nocturnal periods at Fort Calhoun Station, 1973-77.

f

- Te' el 1977 pternet poeternal_

1973 1974 1973 1976 pe. t D1ernal poet gsal Dierns L u_metesmet Diernet secternal Dierne! Docternal tirenst metecust No.

18 4 23 2 321 304 a8.6 74 106 113 115 111 clarerd shed 57 4 8 2 4 1 1 30 31 30.8 Cary 16 7 7 9 67 40.1 l 6 16 4 16 5 1 100 81ect be11 heed 42 7 43 27 8 12 43 18 1 0 73 38 34.2 Channel catfleh 19 -6 2 2 22 31.1 7 17 11 6 4 0 23 St onecat 0 0 0 0 36.6 2 5 6 3 26 15 Flathead catfleh 13 8 4 0 1 1 20 35.7 0 0 21 7 le 1 34 White base 4 7 1 5 16.2 2 2 4 1 SF 11 Creen sunfloh 43 8 0 0 6 0 0 L5 11 3 0 47 23 32.9 8 2 4 10 13 81ees111 4 *? 12 6 0 67 40 37.4 White crapple 14 7 11 17 4 0 0 3 0 0 4 4 40.0 Tellae perch 1 1. 0 0 a 3 27.3 0 3 3 8 sauger 1 0 0 0 0 2 15 83 11 221 260 $ 3.6 Freshwater drum 63 190 27 42 7 14 16 12 9 6 12 81 54.1 ,,

Other 15 33 16 18 10gn 9?4 43.9 Total O

l l

1 Table 2.7.- Susanary of average impingement rates by screen (no. fish /hr per screen) at Fort Calhonn Station, 1973-77.

&creen Date A B C D E F Hay 1973 4.3 1.8 0.2 ' . -

June 0.4 0.4 . 0.5 3.3 1.2 July 1.1 2.3 1.8 2.2 44 11.3 Au8ust 10.4 14.6 3.2 0.7 2.7 1.9.

Sept.=ber 2.9 4.0 0.5 0.5 4.1 1.2 October 5.2 5.0 2.2 1.2 0 0.7 November 6.9 8.3 . 3. 3 2.3 0.9 1.2 December 4.0 0.5 1.1 1.5 1.4 2.7 January 1974 0.8 2.0 0 3.5 1.7 0.7 february 1.2 1.0 0.2 1.7 2.0 1.5 March 0 0 0 1.7 0.5 0.6 April 0 0 0.3 9 0.3 0.2 Hey 1.3 1. 6 ' 1.0 0.8 2.9 1.4 Joe 1.1 1.2 0.1 3.1 0.4 0.3 July  ?.8 1.6 1.3 1.8 1.3 0.6 Au8ust 1.7 1.8 1.0 2.0 2.2 2.5 September 2.3 3.2 1.7 1.6 2.9 0.9 October 3.2 8.1 4.0 4.2 9.8 2.5

- November- 4.0 9.5 18.5 3.2 8.8 2.7 December 0.2 27.7 2.0 1.0 0.2 1.8

, Jeevery 1975 0 0.5 0.8 0.2 0 0.2 February 0 0 0 0 0.2 0.1

_ March 0 1.0 1.5 0 '0.4 0.3 April 0.7 0.3 1.4 2.0 0 0 May 2.4 0.6 0.2 0.6- 0.3 0.9 Joe 1.0 1.3 0.6 0.5 0.3 0.7 July 3.2 7.2 6.7 4.6 2.6 0.2 August 0.9 0.3 0.1 0 0 0.3 September 0.1 0.1 0 0.3 0.4 0 Detober 0.4 0 0.7 0 0.4 0 -

hovember 4.0 . u.7 2.5 3.5 3.2 2.5 December 9.0 5.2 4.2 19.0- 8.6 7.6

-January 1976 1.3 2.7 5.8 5.2 - 10.3 7.7 February 8.4 5.8 -3.2 7.2 4.0 5.0 March 11.4 7.4 8.1 12.7 4.0 12.0

. April 10.6 4.2 3.2 7.4 - 2.9 0.7

- Ney 7.1 4.0- 4.5 3.4 2.0 1.9 June 2.9 1.8 1.0 0.8 1.1 0.7 July 0.2 ' O.4  : 0.3 0.2 0.2 0.1 /

August -- - 3.7 - -

September 0.1

- - - 0.2 0.1 October- 0 0 0 0 0 0 November- 0.5 0.2 2.0 = 1.8 0.7 0.4 December -2.5- 1.2 1.0 0.2 0.5 2.4 January 1977 0.2 1.2 0.2 10 0 0.2 February 2.2 1.0 0.8 0.7 1.0 1.5 March 1.0 0.7 0.2 0 0.3 0.4 April. 4.4 0 . 0 . 0.2 0.2 1.0 May .0.3 0.1 0.1 0.6 0 1.1 June 0 0.1 0.7 0.1 0 0.5 July 0 4.2 0.1 1.7 August 0 1.6 1.0 - 0.1 3.2 0 0.9 0.2 September 1.0 0.3 0.6 1.4 1.1 0.6

.0ctober 0.7 1.9 1.4 0.8 - -

hovembe- 6.7 4.3 7.3 8.6 0 0

. December 1. 4 - 0.6 1.2 0.6 0.5 0.1 a Not sampled.

51 I'

Table 2.8. Projected monthly impingement of fish at Fort Calhoun Station, 1973-77.a Year '

Month 1973 1974 1975 1976 1977 -

January - 5,904 1,152 27.936 1,872 February -

5.328 288 24,336 4,896 March - 2,304 2,304 42,768 1,872 April - 720 4,176 19,584 4.176 May 7,056 6,696 2,016' 21,600 2,736 June 9.792 4,248 2,736 7,200 2,304 July 11,376 5,314 19,296 1,440 6,912 August 11,520 8,280 1,584 1,008 7,200 September 3,024 9,006 1,152 432 4,752 October 7,637 24,912 1,008 -

5.184 November 15,84C 33,264 10,656 3,888 20,736 December- 7.344 5.472 39,168 5.184 3.456 Total 73,S84 111,448 85.536 155,376 66,096 a Projected from hourly impingement rates (no, fish /hr per screen) from daily samples.

52 l

Table 2.9. Comparison of the number of important commercial cpecica impinged at Fort Calhoun .

Station with commercial catch data from the Missouri River, 1974-76.a Channel Flathead Qu111back Catfish Catfish Carp Buffalo and Others Total 1974 2898 892 1783 446 3789 9808 Number impinged Potential harvestable 144 22 80 18C 108 d 372  ;

l fish lostb 11399 Commercial catch (no.) 4417 553 ~4748 1084 597 1975  !

15140 t

Number impinged 7442 2224 1796 2652 1026 42 5 43 10 802 Potential harvestable 702 .

fish lost 3661 488 7768 3528 1067 16509

v. Commercial catch (no.)

• w 1976 Number impinged 26103 2175 1554 4350 4817 38999  ;

58 26 175 24 2188 [

Potential harvestable 1905 fish lost 2817 548 7552 4042 1303 16262 Commercial catch (no.)

i a Commercial catch date from Sioux City, Iowa, to the Platte River (Schainost 1974, 1975, 1976).

b Estimated using calculated annual nortality rates from the Missouri River in 1974 and 1975 (Hesse and Wallace 1976).

C Based on mortality rates for bignouth buffalo. .

d Based on mortality rates for river carpsucker.

_J

. i l

l l

4 l

.l i Chapter 3 FISH LARVAE ENTRAINME!T AND DISTRIBUTION STUDY By Ronald G. King Technical Specification 3.2

+

.=

54

I. Iniroduction The larval fish entrainment study in the Missouri River near Fort Calhoun Station was initiated in April 1974. The goal of the study was to evaluate the impact of Station operation on drifting larval fish that were subjected to condenser and plume entrainment. The study was designed to fulfill monitoring requirements specified in the Environmental Technical Specifications (Omaha Public Power District 1973) and to provide data necessary to meet the Station's NPDES permit. Data on species composition and abundance, horizontal and vertical distribution, and viability of larvae collected from the intake, discharge, and plume locations ware used to determine the impact of Station operation on the larval fish community. Results of the study from 1974 through 1976 have been summarized by Patuiski (1974,1975), Szmania and Johnson (1975), Coon (1976), and Bliss (1977).

Fort Calhoun Station is located along the Missouri River at River Mile 646.0, approximately 20 miles northwest of Omaha, Nebraska, it is a nuclear-fueled f acility with 481 gross megawatt output. Water is drawn from the river

~

into the intake bays with three 120,000 gpm capacity circulating water pumps.

Cooling water is returned to the river immediately downstream of the intake structure through a discharge tunnel that is submerged except during extreme low river flow.

The Missouri River in the vicinity of Fort Calhoun Station is highly channelized and is characterized by swift currents and fluctuating flows.

The-rive.r is approximately 600 ft wide and 15 ft deep near the Station and ,

maintains an average flow of 28850 cfs. The river channel is maintained for navigation by trail dikes, winc dans, and revetments.

II. Materiale and Methods Larval fish samples were collected with two no. 0 (571 p) mesh nitex

. plankton nets suspended from booca attached to each side of a boat. A flow meter (General Oceanics Model 2030) was attached in the mouth of each net to determine the collection velocity and the volume of water sampled. Samples were collected with 0.5 m diameter nets in 1974 and 1975 at a collection duration of 3-7 min. In 1976 and 1977, 0.75-m diameter nets were employed and collection duration wat reduced to 1-3 min. The larger r.et and reduced collection duration were implemented in an attempt to reduce collection mortality, and still maintain an adequate sample size. In addition to the lerger nets in 1976, collection buckets were switched from screened to un-screened buckets in an effort to further reduce colle tion mortality. All entrainment and horizontal distribution samples wert allected from the upper meter of water, except at the discharge location, from mid-June 3976 through 1977. In 1976, a freme was installed at the end of the discharge tunnel to provide a means by which plankton nets could be lowered over the discharge port. This allowed discrete samples to be collected from the discharge.

Duplicate samples were collected at each of six locations (Figure 3.1) for analysis of entrairment ef f ects from mid-April through early August 1974, 1975, and 1976. Larvae from each sample were manually separated into live 55 l

I.

1 and dead fractions within 20 to 60 min after collection using illuminated magnifiers. At the conclusion of each survival analysis, all larval fish ware preserved in 4% f ormalin f or later identification.

During the 1977 study, entrainment sanples were collected only at the intake, discharge and plume locations (Figure 3.1) . Duplicate samples were collected at the discharge and plume locations, whereas eight replicates were collected at the intake. The additional intake replicates were collected over a range of velocities in an effort to determine net-induced mortality. In addition to making live-dead determinations in 1977, the dead larvae were further separated into opaque and transparent groups.

The cross-channel distribution of larval fish was determined by sampling three locations along a transect immediately upstream of the Station (Figure 3.1).

Larvae f rom entrainment samplen were used to determine horizontal distribution in 1974 and 1975. In 1976 and 1977, 10 replicate samples were collected at each location along the transect to establish a broader data base for statio-tical comparisons. An assessment of vertical distribution of larval fish was not attempted until 1977 because of high river velocity and the difficulty in obtaining mid-depth and bottom samples f rom the Missouri River. Vertical pro-files were determined on 29 occasions between 14 June and 8 August 1977 by Omaha Public Power District personnel. Single samples were collected near the intake (Figure 3.1) with a 0.75 m, no. 0 (571 u) nitex plankton net from the surf ace, mid-depth, and 1 m above the bottom.

Chi-square analyses were used to test for significant dif ferences (p 10.05) in larval mortalities between locations. In addition, the "Unifozuly Most Powerful Test for Poisson Means" was performed on the transect data to dstermine significant differences (p 10.05) in horizontal distribution in 1974 and 1975. Statistical differences among transect locations in 1976 and 1977 were te.sted with a one-way ANOVA and Tukey's multiple comparison procedure.

III. Results and Discussion A. Species Composition and Abundance Larval fish generally were present in the drif t near Fort Calhoun Station from early May through July. Bimonthly macroinvertebrate entrainment studies (Carter 1978) indicated that larvae did not occur in the drift prior to mid-April when ambient water temperatures were generally less than 13C. The earliest date on which a larval fish was collected was 17 March 1977 when a single burbot (Lota lota) was taken f rom the discharge. Fish larvae were rela-tively sparse in the drif t by late July and were absent by mid-August. Peak larval densities occurred from mid-June through mid-July (Figure 3.2) when ambient water temperatures - nged from 21 to 25C. Densities greater than 100

' larvae /100 m3 were generally associated with the occurrence of freshwater drum in the drif t.

The larval fish assemblage in the Missouri River was dominated by freshwater drum, catostomids, carp, and Stizostedion sp. (Table 3.1). Freshwater drum wete the most abundant larvae collected, comprising f rom 43.7 (1974) to 88.2% (1977) of the_ total yearly larval catch. Catostomids, including carpsucker 56

l 4

(Carpiodes sp.), white sucker, buf f alo (Ictiobus sp.), and redhorse (Moxostosa sp. ) were the second most common larvae encountered. Combined, freshwater drum end catostomide accounted for 95.4% of the larvae collected during the study.

The occurrence of larval fish in the drif t followed similar patterns throughout the 4-year study. The sauger-walleye group (Stizostedion sp.)

and Catostomidae, primarily Ictiobus sp. , were the dominant taxa in May and freshwater drum and catostomids, primarily Carriodes sp., were dominant from June through July (Figure 3.3). The relative abundance of larvae did not necessarily correspond _ to the relative abundance of adult fish present in the vicinity of the Station (Table 1.1) . Game fish, including white bass, Lepomis sp. , yellow perch, Pomoxis sp. and sauger-walleye comprised less than 1% of the larvae collected. These fishes are either nest builders or random spawners which lay adhesive or demersal eggs. Spawning characteristics combined with .

low relative abundance of adults near the Station probably account for the low occurrence of game fish larvae in the drift. In contrast, freshwater drum comprised 3.9% of the adult fish in the vicinity of the Station in 1977; however, 90% of the larvae in the drif t were drum (Table 3.1) . Freshwater drum are pelagic spawners (Davis 1959; Nelson et al. 1967) which probably accounts for the high relative abundance of drum larvae in the drif t. Other fishes that are either random or pelagic spawners whose larvae ccamonly occurred in the drift included carp, catostomids, gizzard shad, and goldeye which are common species in the vicinity of the Station (Table 3.1).

Upstream sources of fish larvae drif ting past Fort Calhoun Station have not been well documented. Sources of larvae would include discharges f rom Lewis aad Clark Lake, the unchannelized river between Yankton, South Dakota and Sioux City, Iowa, tributary streams, sloughs, and other protective bankline features along the channelized river such as revetment holes and dike backwaters. Walburg (1971) estimated that peak 24-hr larvae losses f rom Lewis

-and Clark Lake, a main stem Missouri River reservoir, included 10 million f reshwater drum, 800,000 cyprinids and 700,000 sauger-walleye. Sources other -

than- discharges f rom Gavins Point Dam may be more important, because Cada (1977) estimated that 400-500 million larvae pass Fort Calhoun Station per day during peak larval drif t. The distribution of adult fishes in the unchannelized and channelized Fussouri River generally indicates that all fishes whose larvae were collected near Fort Calhoun Station have videspread distributions. However, sauger have spawning concentrations in the tailwaterF of Gavins Point Dam and at the confluence of tributary streams (Could and Schuulbach 1973).

B. Distribution The horizontal distribution of larval fish war determined on each sampling date to estimate the percentage of larvae that were exposed to entrain-ment. Results of the transect studies indicated significantly (p 10.05) higher densities along the cutting bank of ' the river, adjacent to the Station's

> intake structure (Figure 3.4) . Densities generally were lowest at the mid-channel location. Larval dencitles near the filling bank varied but were generally similar to those at the mid-channel location. This heterogeneous distribution across the river has been attributed to hydraulic f actors which y tend to concentrate driftirg particles along the cutting bank (Harrow et al.

>- 1975). Species composition was similar along the transect (Table 3.3).

57 h I l

l

- . _ .. - - . - - . - ~~ -. _ .

The vertical distribution of larval fish in the Missouri River has not been as extensively studied as horizontal distribution because of high river veloc.* ty and the dif ficulty in obtaining mid-depth and bottom samples.

Data collected from the intake and discharge locations suggest that larvae also exhibit a heterogeneous vertical distribution. Intake densities averaged approximately 55% higher than disaharge densities over the 4-year study (Table 3.2). Dif ferences between locations generally were most pronounced during peak periods of larval abundance, which corresponded to high relative abundance of dreshwater drum.

The majority of cooling water entering the intake structure is withdrawn f rom the lower portion of the water column (Omaha Public Power District 1976); therefore, the heterogeneous vertical distribution of larvae, resulted in lower discharge densities that represented a mean of the water column. The importance of this vertical distribution was evident when the percentage of entrained larvae was estimated using surface densities at the intake. Since little surf ace water is entrained through the circulating water system, larval densities f rom the surf ace samples everestimated the percentage of entrained larvae.

In 1977. the vertical distribution of larvae va. determined near the intake structure by Omaha Public Power District personnel, The results of this study documented a significant (p 10.05) decrease from surface to bottom in vertical distribution (Omaha Public Power District, unpublished data). Mean surface and bottom densities differed by a factor greater than three. Data on species composition from the vertical distribution study were unavailable upon preparation of this report; however, there were no consistent differences in species composition between the intake and discharge samples.

The diurnal distribution of larvae in the Missouri River has not been ,

-extensively studied. However, collections have been made over 24-hr periods in the vicinity of Fort Calhoun Station (Cada 1977; Omaha Public Power District, unpublished data). The results of these studies indicate that although variations in densities were noted over a 24-hr period, no significant dif ferences (r > - 0.05) between mean day and night densities were encountered. Cada (1977) concluded that reples collected at mid-morning adequately represented the 24-hr mean. Higo turbidity and velocity of the Missouri River may reduce the diurnal periodicity that has been reported for fish larvae. Gammon (1976) suggested that the lack of diurnal changes in distribution on the Wabash River may be attributed to turbidity.

C. Entrainment Effects Discharge mortalities at Fort Calhoun Station averaged 86.4% over the 4-year study. During June and July, when larvae were present in suf ficient abundance to determine entrainment losses, discharge mortalities ranged from 57 to 95% (Figure ~3.5). High entrainment losses were associated with the occurrence of freshwater drum larvae in the drif t. Freshwater drum, which accounted for nearly 75% of the entrained larvae, experienced 96% mortality upon condenser passage. Catostomids were the only other taxa collected in 58

suf ficient numbers to determine survival following condenser passage. During the study nearly 51% of the catostomids collected f rom the discharge were alive.

Based on the physical characteristics of the Missouri River (including high current velocities, turbulent flow, and heavy detritus, silt, and sand loads), it was assumed that less than 100% of the larvae in the drift were alive.

Prior to 1977, intake morta11 ties generally were similar to or greater than morta11 ties reccrded from the discharge and plume samples. High mortalities at the intake were attributed to both natural and net-induced mortality. The current velocity along. the cutting bank of the Missouri River normally exceeded 100 cm/sec, while the discharge velocity at normal river level was approximately 60 cm/sec. Mortality of fish larvae when collected with a plankton net has been shown to increase with velocity (McGroddy and Wyman 1977) . The results of a recent study conducted by Cada (1977) on the Missouri River indicated that a linear relationship exists between percent mortality and net velocity. Data collected in 1977 indicated that when intake samples were collected at or below the discharge velocity, significantly higher (p 1 0.05) mortalities were noted in the discharge as a result of condenser passage.

Data collected in 1977 indicated that nearly 62% of the' larvae were dead at the intake location (Table 3.3), it is probable that net induced morta11 ties occurred even though collection velocities were reduced. Data obtained from separation of opaque and transparent dead larvae ' indicated the natural mortality at the intake was less than 60%. The criterion used in the Fort Calhoun study for determining dead larvae was the lack of visceral movement upon probing. Other studies have used opacity te make live-dead determinations (Marcy 1976). In 1977 opacity was used at Fort Calhoun Station as a means of separating natural mortality from net-induced mortality. It was assumed that dead transparent larvae were recently killed and could be attributed to net-induced mortality. The amount of time required for live transparent larvae to become opaque upon death was determined for larvae collected from both the intake and discharge. Larvae f rom both locations required approximately 1-2 hr to turn opaque af ter being killed. Since each live-dead separation was com-pleted within 20-40 min af ter collection it was assumed that transparent larvae were killed by collection. It is unknown whether.the transparent dead larvae

- from the discharge were killed by the collection technique or condenser passage.

Net-induced mortalities can occur at collection velocities of 60 cm/sec or less (McGroddy and Wyman 1977; cada 1977). Furthermore, it is not known how soon color change occurs when larvae are subjected to a sudden temperature elevation.

Based on available data, it was assumed that the opaque larvae at the intake represented-natural mortality and at the discharge the opaque larvae repre-sented natural and condenser passage mortality. However, the possibility exists that a greater percentage of dead opaque larvae occur in the lower portion of the water column where most of the cooling water is withdrawn.

Differential mortalities (discharge minus intake mortality) in 1977 ranged f rom 10.2 to 50.2% when sampling eff ects were not taken into account (Table 3.4). A more conservative estimate of condenser mortelity was made by assuming that the transparent dead larvae were alive prior to collection, as discussed above. This approach indicated that condenser passage caused mortal-ities that were 12.6 to 55.5% greater than intake mortalities-and totaled 44.3%

59 l

during the 1977 larval fish season, compared to 27.9% when sampling ef fects ware not taken into account (Table 3.4). Significantly (p 1 0.05) higher mortalities occurred in the discharge when larvae were abundant enough to determine entrainment effects.

Condenser passage effects at Fort Calhoun Station probably were related to a combination of thermal and mechanical factors; however, the narrow range of Strtion operating conditions during the period when studies were con-ducted and the short period of peak larval densities precluded the isolation of the factors involved. Entrainment effects could only be directly related to thermal f actors since the data were collected during periods of heat exchange.

Marcy (1976) suggested that size-related mechanical effects are more important than thermal ef fects. The mean total length of f reshwater drum larvae collected near Fort Calhoun Station increased f rom approximately 4.5 mm on 1 June to 7.1 mm on 13 July 1977. This increase in mean total length did not consistently result in higher discharge mortalities (Table 3.4) .

Absolute discharge temperatures increased during each summer since the Station went on line in 1973 without resultant increases in discharge mortalities (Figure 3.5) . Marcy (1976) found that no larvae survived in a discharge canal when the temperatures were 29.0-33.5C. Since absolute discharge tcmperatures generally exceeded 30C at Fort Calhoun Station, 100% mortality could be expected. The relatively high survival (14% over the 4-year study par!< d) in the discharge was probably related to the short exposure to absolute disc sge temperatures (2 min). Entrainment effects were not related to AT which ranged from 7.2 to 11.0C during the study. The 1977 data, whic.h took samplin4 ef fects into consideration, suggest that nearly 30% of the larvae Entrained may survive condenser passage.

Effects of plume entrainment were determined from data collected at the 1C isotherm. No effects were detected during the 4-year study th.at could be attributed to Station operation. Mortalities observed in the plume were similar to those at the intake on most sampling dates. Net-induced mortalities may have masked effects prior to 1977; however, intake and plume data from 1977 were similar to those from the previous three years. Species composition was the same upstream and' downstream of the Station. Furthermore, the percentage of opaque dead larvae (representing natural mortality) was the same at both locations in 1977.

Larvae densities were generally lower in the plume when compared to those in the intake (Table 3.2). The reason for this lower density is not known but it may be related to the heterogeneous cross-channel distribution.

Plume samples were collected 1 to 5 miles downstream of the Statiot, and in

. this river segment the main channel is on the Iowa shore. Therefore, the plume samples were collected near the filling bank of the river, while the intake samples were collected from the cutting bank where larval densities were generally highest. Intensive sampling along downstream transects may be necessary bef ore plume entrainment effects can be fully evaluated. However, based on the mixing characteristics of the submerged discharge, the rapid dissipation of heat, the short exposure time to elevated temperatures in the plume (approximately 20 to 120 min), and the low percentage of river water used for cooling, the impact of plume entrainment is probably less than the L= pact of condenser passage.

60

-- . ~

_ _ . _ _ .______ . . . _ . _ _ ~. _ . _ _ _ __

+ 4 D. Impact The impact assessment of entrainment -losses at Fort Calhoun Station was bascd on cooling water usars, species composition, abund; ce, distribution, and survival data. The Station entrained 1.8 to 12.4% of the total larval assemblage during the -study (Table 3.5). The most conservative impact estimate would be based on 100% mortality of the entrained larvae. If 100%. mortality isLassumed, average entrainment losses-were 5.3%. However, 14% of the larvae '

-collected from the discharge survived condenser passage; theref ore, the average entrainment loss would be 4.6%. A more realistic estimate of entrainment losses was determined using data from 1977. The alteration of sampling

- procedures in 1977 resulted in a discharge' mortality that was 44.3% greater than the intra.e mortality. Based on these dats, mortality for the total larval assemblage passing the Station increased 2.6% in 1977. Inferences on the impact of entreinment losses would be speculative without data on standing crop and natural mortality' levels of the life stages of the species entrained.

3

- The freshwater drum population in the Missouri River was potentially the most affected:by entrainment. This species was predominant in the drift and experienced the greatest entrainment losses. Freshwater drum spawn plank-tonic eggs and the prolarvae are semibouyant which may account for the high relative abundance in the drif t (Swedberg and Walburg 1970). During 1977, an Eestimated 3.3-billion larvae passed the Station between 13 May and 25 July, of which 2;9 billion were f reshwater drum. The number of adult female fish required to produce these larvae can be estimated using fecundity data. Based on fecundity data of f reshwater drum in Lewis and Clark Lake, the larvae collecteu near Fort Calhoun Station would represent the production of nearly 90000 female freshwater drum. This is a minimum estimate and could be many ,

times greater if. mortality rates for freshwater drum are as high as those reported for other species (Marcy 1976). A recent population estimate for a segment of the channelized Missouri River (Bliss 1978) suggests that the number of adult freshwater drum'in the channelized river above Fort Calhoun-Station is too low to acccant for this production. The impact of entrainment losses-on the freshwater-drum population downstream of the-Station depends on the eventual fate of larvae in the drift. It is not known if the river population depends on larval-drift for recruitment. The possibility exists that contri-butions from spawning areas downstream of the Station could of fset entrainment losses _(<5%) of freshwater drum.- Further studies would be required to identify sources of larvae in the drift.

Entrainment at Fort Calhoun Station has a lower potent 1a1 impact on larval fishes other thanL freshwater drum. Game fishes were entrained sporadically and' generally at low densities. In addition, catfish larvae were not collected from the drift which minimizes the impact on these important commercial ~ species.

- IV. Summary and Conclusions

1. Potential impact on game fish (including sauger-walleye and white bass) and important commercial fish (including carp, channel catfish, and flathead catfish) was low because larvae of these species generally comprised a low percentage of the entrained ichthyoplankton.

61 ,

i y -- -. , ,_..-c , . _ , . . . .-,m. . . _ - _ , _ _ _ - - . . . _ . - , _ . . , - . - - . . - - -

r 4

2. Catostomids were entrained throughout the lartal season but over 50% survived condenser passage during the 4-year study.

3. Freshwater drum accounted for 75% of the entrained larvae and 96%

collected la the discharge were dead.

4. Entrainment effects were determined only duriug periods of heat transfer which prevented the separation of mechanical from thermal effects.

5. Survival following condenser passage was nearly 30% in 1977 when discharge temperatures ranged f rom 29 to 370.

6. Survival of larvae at temperatures above 30C was attributed to the short duration of exposure (2 min) to absolute discharge temperatures.

7. The mixing characteristics of the submerged discharge, rapid dissipation of heat, short exposure to plume temperatures, and the low per-centage of r!.ver water used for cooling reduced the impact of plume entrainment.

8. The Station entrain'ed 1.8 to 12.4% of the larvae passing the S ta tion.

9. Estimeted entrainment losses ranged from 2.6 to 5.3% of the total larval assemblage.

62

V. References Cited Bliss, Q. P. 1977. Fish larvae entrainment and distribution study. Pages 75-95 in S. R. Carter, ed. Operational environmental monitoring in the Missouri River near' Fort Calhoun Station, January 1976 through December 1976. (Project No. 5501-07676). Report prepared by RALCO Environmental Sciences for Omaha Public Power District. Omaha, Nebr.

. 1978. Estimation of fish population in the Missouri River near the Nebraska City Power Station, November 1977. (Project No.

5501-08880). Report prepared by RALCO Environmental Sciences for Omaha Public Power District, Omaha, Nebr.

Ca da , G . F . 1977. The entreinment of larval fishes at two nuclear power plants on the Pussouri River in Nebraska. Ph. D. Thesis. Univ. Nebraska, Lincoln. 133 pp.

Carter S. R. 1978. (In press). Macroinvertebrate entrainment study at Fort Calhoun Station on the Missouri River .near Blair, Nabraska. Fourth National Workshop on Entrainment and.1mpingement. . Ecological Analysts, Melville, H. Y.

Coon D. M. 1976. Fish larvae entrainment study. Pages 77-96 in D. L.

Wetzel, ed. Operational environmental monitoring in the Missouri River near Fort Calhoun Station, July 1975 through December 1975. (Project No.

5501-06392). Semi-annual summary report by NALCO Environmental Sciences for Omaha Public Power District, Omaha, Nebr.

Davia C. C. 1959. A planktonic fish egg from fresh water. Idanol. Oceangr.

4(3):352-355.

Gammon, J. R, 1977. Measurement of entrainment and predictions of impact on the Wabash and Ohio Rivers. Pages 159-176 irt L. D. Jensen, ed. Third national workshop on entrainment and impingement. Ecological Analysts, Inc., Melville, H. i.

Could, G. , and ' J. Schmulbach, 1973. Relative abundance and distribution of fishes in the Missouri River, Gavins Point Dam to Rulo, Nebraska. Final Rep. Missouri River Environ. Inventory. U. S. Army Corps of Engineers, Omaha, Nebr. 60 pp.

l l

Harrow, L. G. , I. Cherko, and A. B. Schlesinger. 1975. Seasonal and distri-l butional patterns of ichthyoplankton in the Missouri River. Environmental Series Bull. No. 1. Omaha Public Power District, Omaha, Nebr. 19 pp.

Marcy, B. C. 1976. Planktonic fish eggs and larvae of the lower Connecticut River and the ef f ects of the Connecticut Yankee Plant incivding entrain-ment. Pages 115-140 in D. Herriman and L. M. Thorpe, eds. The Connecticut River ecological study: the impact of a nuclear power plant. Am. Fish.

Soc. Monogr. No. 1.

McGroddy, P. M., and R. L. Wyman. 1977. Efficiency of nets and a new device f or_ sampling living fish larvae. J. Fish. Res. Board Car. 34:571-574.

63 l __ _ - ._. - - , . . .- -

I N21 son, W. R., R. E. Seifert, and P. V. Swedberg. 1967. Studies of the early life hictory of reservoir fishes. Pages 374-385 in Reservoir Fishery Resources Sympcsium, Southern Division. American Fisheries Society.

University Georgia Press, Athens.

Omaha Public Power District. 1973. Environmental technical specifications for Fort Calhoun Station Unit No. 1. Appendix B, Docket No. 50-285. 11 pp.

. 1976. Intake monitoring report: Fort Calhoun Station Unit No. 1.

Omaha Public Power District, Omaha, Nebr. 144 pp.

Patulski, D. E. 1974. Fish larvae entrainment study. Pages98-121 in K. E.

Bremer, ed. Operaticnal environmental monitoring in the Missouri River near Fort Calhoun Station, January 1974 through June 1974. (IBT No. 643-04254).

Semi-annual report by industrial BID-TEST Laboratories, Inc. for Omaha Public Power District, Omaha, Nebr.

1975. Larval fish entrainment study. Pages90-136 in D. L.

Wetzel, ed. Operational environmental monitoring in the Missouri River n2ar

-Fort Calhoun Station,. July 1974 through December 1974. (IBT No. 643-04254).

Semi-annual report by Industrial BIO-TEST Laboratories Inc. for Omaha Public Power District, Omaha, Nebr.

Swedberg, D. V., and C. H. Walburg. 1970. Spawning and early life history of the freshwater drum in Lewis and Clark Lake, Missouri River. Trans.

Am. Fish. Soc. 99(3):560-570.

Szmania, D. C. , and D. L. Johnscu. 1975. Fish larvae entrainment study summary. Pages 73-91 in D. L Wetzel, ed. Operations 1 environmental monitoring in the Missouri River near Fort Calb)un Station, January 1975 through December ~1975. (IBT No. 643-06392), hemi-annual su:nmary report by Industrial BIO-TEST Laboratories, Inc. for Omaha Public Power District, Omaha, Nebr.

Walburg, C. H. 1971. Loss of young fish in reservoir discharge and year-class survival, Lewis and Clark Lake, Missouri River. Pages I:41-44d in G. E.

Hall, ed. Reservoir fisheries and limnology. Am. Fish. Soc. Spec. Publ.

No. 8.

64

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APR MAY JUN JUL AUG Figure 3.2. Seasonal abundance of larval fisn in the Missouri River near Fort Calhotm Statio%

1974-77.

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FRESHWATER DRUM MAY JUN JUL ' AUG Figure 3.3. Seasonal abundance of the jor fish larvae taxa in the Missouri River near Fort Calhoun Station, 1976.

67

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Table 3.1. Surzsary of the relative absudance of adult and larval fishes in the Missouri River near Fort Calhoun Station. 1974-77.

Relative Abundance G) 1974 1975 1976 1977 Taxa 1.arvae Adult I.arvae Adult Larvae Adult I.a rvae Adult Scaphirhynchus sp. 0.0 0.0 0.0 0.0 <0.1 0.0 0.0 0.0 Gizzard shad 2.5 7.5 1.6 19.8 2.9 10.8 3.1 4.0 Coldeye 0.1 11.0 0.1 25.9 <0.1 10.8 <U.1 15.2 Carp 3.7 57.4 3.0 30.2 0.7 33.4 0.8 28.4 Cyprinida6 1.7 --

1.4 -- 0.6 -- 0.8 --

$ 11.7 16.4 17.2 Catostomidae 38.3 17.0 15.5 9.5 6.3 White bass 1.4 0.3 0.6 0.0 G1 2.3 0.3 0.1 l

0.2 0.3 0.8 0.0 <B.1 2.5 <0.1 0.3 t

Lepomis sp.

Pomoxis sp. 0.4 0.6 0.1 0.0 <0.1 5.9 0.0 0.1 Percidae 0.1 - 0.0 -

<0.1 --

<0.1 -

Yellow perch 0.0 0.0 0.0 0.0 <0.1 1.4 <0.1 0.0 Stizostedion sp. 5.6 0.6 1.6 0.9 0.4 0.8 0.2 0.7 Freshwater drum 43.7 0.6 73.7 6.0 83.4 3.4 88.2 3.9 Unidentified 2.3 -- 1.7 - 0.2 - 0.3 -

p gg a

,a

Table 3.2. Summary of intake, discharge, and plume densities (no. larvae /

100 mJ) in the Missouri River near fort Calhoun Station. 1975-77.

Date intake Discharge Plume 14 May 1975 6.1 5.2 5.9 29 May 10.7 42.0 16.2 4 June 34.8 28.8 14.7 12 June 46.5 22.5 26.2 19 June 80.5 71.8 73.S 26 June 295.0 102.0 214.7 2 July 443.8 214.9 63.0 8 July 77.9 65.5 52.9 23 July 14.2 4.1 6.8 20 May 1976 11.8 3.4 2.3 2 June 33.1 20.4 15.0 9 June 130.0 170.0 99.5 16 June 549.0 288.6 264.5 23 June, 106.8 125.1 82.0 30 Jure 620.0 120.5 238.5 7 July 252.7 125.8 88.7 14 Jvly 26.9 92.8 29.6 29 July 30.4 51.3 7.6 25 May 1977 16.2 15.1 23.5 1 June 53.4 58.3 27.0 6 June 177.0 116.5 50.0 15 June 563.0 351.0 210.0 23 June 137.4 48.2 45.1 >

30 June 111.4 68.4 141.2 6 July 130.0 30.3 51.2  !

13 July 72.0 52.9 14.7 25 July 10.7 3.9 5.2 71

- - ,. . - - , . - . - - . - . - . . . . - . . , - - . - - . . . - - . . ~ - . - - _ . - . . - . .

Table 3.3. Relative abundance (%) of fish Icrvan ct three croso-chennel locations in the Miocouri River near' Fort Calhoun Station, 1974-77.

1974 1975 1976 1777 Taxa 1 3 4 1 3 4 1 3 4- 1 3 4 Scaphithynchus sp. 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 <0.1 0.0 Gizzard shad 3.5 0.0 4.6 2.9 0.6 2.4 3.1 2.2 3.3 3.9 2.2 6.3 Coldeye 0.0 1.3 0.0 0.1 0.0 0.2 0.0 <0.1 0.0 <0.1 1.0 0.3 Carp. 2.8 9.5 1.2 3.7 4.1 3.4 0.6 1.2 0.6 1.1 1.7 1.1 Cyprinidae 1.9 6.2 3.3 2.3 0.9 1.4 0.7 0.6 0.8 2.9 3.9 6.1 Catostomidae 47.3 40.5 39.2 14.3 13.4 15.5 8.2 19.0 14.3 5.5 11.6 9.7 Burbot '

O.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 <0.1

White bass 0.5 4.0 2.5 0.4 0.8 0.5 0.1 0.1 0.1 1.3 0.2 0.2 j Leposts sp. 0.3 0.0 0.0 0.0 0.0 0.2 <0.1 <0.1 <0.1 0.2 <0.1 0.2 Pomoxis sp. 0. 3 - 0.0 0.7 0.1 0.0 0.0 0.0 0.0 <0.1 0.0 <0.1 0.0 Percidae. 0.0 0.0 0.0 0.0 0.1 0.0 <0.1 <0.1 0.0 <0.1 0.0 <0.1

} Tellow perch U.0 0.0 0.0 0.0 0.0 0.0 <0.1 <0.1 <0.1 <0.1 <0.1 <0.1

, ,, Stizostedion sp. 6.4 1.7 1.4 2.5 0.1 1.4 0.5 0.1 0.3 0.3 0.3 0.4 N Freshwater drum 35.8 33.4 46.5 72.1 78.0 71.7 86.7 76.4 80.4 8&.7 78.8 75.5 Unidentified 0.8 3.4 0.6 1.4 2.0 1.9 <0.1 0.3 0.2 0.0 0.0 0.0 e

i 4

r i

I i I 1

e l

i .

I

4 Table 3.4. Condenser passage ef fects on larval fish following entrainment at Fort Calhoun Station, 1 June-13 July 1977.

i j Intake Discharge Alive (%) Dead (%) Alive (%) Dead (I) Differential Date- Opaque Transparent Opaque Transparent Mortality (%)*

1 June 1977 .

Freshwater drum 45.6 29.1 25.3 5.9 76.5 17.6 39.7 47.4 Total Larvae 46.9 29.6 '23.5 12.5 66.7 20.8 34.4 37.1 6 June 1977 j Freshurter drum 34.2 35.0 30.8 3.6 85.7 10.7 30.6 50.7 i

Total Larvae 36.2 34.9 28.8 5.0 83.3 11.7 31.2 48.4 i

I 15 June 1977

~4 Freshwater drum 22.6 30.7 46.7 1.3 81.5 17.2 21.3

" 30.E

Total Larvae 22.7 31.2 45.1 1.9 79.9 18.2 20.8 48.7 l

23 June 1977 Freshwater drum 48.6 20.6 30.8 14.3 64.3 21.4 34.3 43.7 Total Larvae 52.5 19.6 27.9 42.3 42.3 15.4 10.2 22.7

, 30 June 1977 Freshwater drum 57.8 16.0 26.2 14.3 71.4 14.3 43.5 55.4 Total Larvae 58.5 17.7 23.8 19.4 54.8 25.8 39.1 37.1 I- 6 July.1977-i

~

Freshwater drus 56.5 16.7 26.8 6.2 81.2 12.5 50.2 64.5 Total Larvae 56.2 16.6 27.2 16.7 72.2 11.1 39.6 35.6 13 July 1977

Freshwater drum 57.1 14.1 ' 28.8 23.1 15.4 61.5 34.0 i 1.3 Total Larvae 56.0 14.1 29.9 20.0 26.7 53.3 36.0 12.6 j

O Dif ferences between intake and discharge mortalities are based on I alive (Column 1) and I opaque (Column 2).

\

i

i-i Table 3.5. Sutmaary of cooling v::ter use and entrainment rates of larval fish through Fort Calhoun i Station, 1974-77..

River Flow Cooling Water Use Percent of Missouri River Number of Larvae Date (cfs) (I River Flow) Fish Larvae Entrained Entrained per 24 hr 7 May 1974 32,000 2.5 -12.4 131,000 ,

24 May 33,000 2.4 9.8 606.000 5 June 33,500 2.4 -

5.3 847,000 18 June 35,000 2.3 6.1 1,265,000 9 July 34,500 2.3 4.9 745,000 la May 1975 38,000 2.1 2.1 78,000 29 May 40,500 1.9 4.1 210,000

) 4 June 40,000 2.0 3.0 683.000

, 12 June 44,500 1.8 3.8 912,000 i 19 June 52,700 1.5 2.4 1,579,000 26 June 48,500 1.7 2.2 5.786,000 2 July. 51,500 1.6 2.1 8.704.000 8 July 53,000 1.5 2.7 1,528,009 23 July. 59,000 1.4 1.8 279,000

% 6 May 1976 39,000 2.1 9.0 35,000 20 May 37,000 2.2 10.0 208,000 1 2 June 38,500 2.1 3.9 410,000

! 9 June 40,000 2.0 3.5 3,562.000 j 16 June 39,800 2.0 5.7 11,097,000

! 23 June 39,100 2.1 5.2 2.826,000

) 30 June 42,600 1.9 5.3 11.064,000 l 7 July 40,900 2.0 6.4 4.872,000

~i

14. July 39,300 2.0 6.0 1,606.000 29 July 40,700 2.0 3.5 502.000 12 May 1977 31,600 2.5 2.5 81,000 25 May 31,700 2.5 4.4 550,000 1 June 31,900 2.5 3.8 1,377,000 6 June 31,400 2.6 9.1 2.956,000

.l 15 June 35,100 2.3 9.2 10,128,000 l

23 June 33,300 2.4 6.4 3,334,000 30 June 33.500 2.4 4.7 3,009,000 6 July 33,100 2.4 4.5 2,687.000 13 July 34,500 2.3 4.7 1,514,000 l 25 July 37,700 2.1 8.3 573,000

_h