ML20079D347
| ML20079D347 | |
| Person / Time | |
|---|---|
| Site: | Mcguire, McGuire  |
| Issue date: | 06/30/1991 |
| From: | DUKE POWER CO. |
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| NUDOCS 9107110188 | |
| Download: ML20079D347 (100) | |
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-1 I
i 1.AKE NORMAN: 1990
SUMMARY
MAINTENANCE MONITORING PROGRAM McGUIRE. NUCLEAR STATION: NPDES No. NC0024392 l I i DUKE POWER COMPANY n . Production Environmental. Services, TTC/ASC 13339 Hagers Ferry Road Huntersville, North Carolina 28078-l 1 I r r i i JUNE, 1991 . 3 9107110109 910701 i ADCK;K 030003A9 PDR
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F 1 LAKE NORMAN: 1990
SUMMARY
Pace
!. EXECUTIVE
SUMMARY
11
- 11. MNS OPERATIONAL DATA Operational Characteri stics - 1990 . . . . . . . . . . . . . . . . . . . . . 1 111-TEMPERATURE AND DISSOLVED OXYGEN Introduction ........................................ .. 4 Methods and Materials .................................. 4 Results and Discussion ................................. 6 future Studies ......................................... 12 Summary ................................................ 12 IV. WATER CHEMISTRY Introduction ........................................... 37 Methods and Materials .................................. 37 Results and Discussion ................................. 38 Future Studies ......................................... 40 Summary ................................................ 41 !
V. PHYTOPLANKTON Introduction ........................................... 49 Methods and Materials .................................. 49 Re s ul ts and Di scu s si on . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 50 ; Summary ................................................ 53 VI. ZOOPLANKTON _ introduction ........................................... 63 Methods and Materials-.................................. 63 : Res ul t s a nd D i sc u s s i on . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 63 Summary ................................................ 66 j Vil FISHERIES Introduction ..................................-......... 74 _ , Methods and Materials .................................. 74 Results and Discussion ................................. 75 Future Studies'......................................... 77 : Summary ................................................ 17 7 P i a.-.__.a._._.....____ . _ _ _ _ _ - . _ _ _ _ _ . . _ . _ _ . _ _ _ . _ . _ _-_ _ = _. _ __ _ _ __ ____. - __ _ ._
- 1. EXECU11VE
SUMMARY
This report summarizes the 1990 results of the 1.ake Norman aquatic environment maintenance monitoring program, as required by NPDES Permit No. 0024392, for McGuire Nuclear Station. The overall capacity factor for McGuire during 1990 was 56.6%, in contrast to 77.1% in 1989. The average monthly discharge temp-eratures were 96.9. 96.5, and 92.5 F for July, August, and September, respectively; these were below the NPDES-permitted monthly average of 99 F for those months. The thermal and oxygen dynamics of 1.ake Norman in 1990 were similar to other southeastern reservoirs of comparable size and trophic status. Aerial infrared imagery of the lake, with McGuire's discharge at 99 F, indicated a 5 F-above background plume of 730 acres around MNS, and a 90 F surf ace plume of 386 acres around MNS, both substantially smaller than earlier modeling studies had pre-dicted under worst-case meteorology. Water temperatures in 1990 were up to 3.5 C cooler than winter 1989, and up to 4.1 C warmer than other seasons in 1989, with temporal and spatial trends as in prior operating years; these seasonal differences between years were attributed to meteorological dif ferences and to increased 1990 pumping operations (423' ) at Marshall Steam Station relative to 1989. Spring and summer dissolved oxygen ranged up to 2.2 mg/L lower than observed historically, reflecting the concurrent thermal differences; other D0 values and temporal / spatial trends were similar to previous years. All water chemistry parameter., (turbidity, specific conductance, pH, alkalinity, major cations and anions, nutrients, and metals) were within the historical ranges previously reported for I.ake Norman during both MNS-operating and pre-operational years. Phytoplankton and zooplankton standing crops showed a trend of increasing values from downlake to uplake locations, as in previcus years. Seasonal com unity composition remained relatively stable between years, and the annual ranges in standing crop values were similcr to 1988 and 1989. Phytoplankton and zooplankton communities were dominated by diatoms, green algae, chrysophytes, cryptophytes, rotifers, and copepods. 1 ii
3 4 i McGuire's thermal discharge clearly affected localized fish distribution, but evidently caused no direct mortalities or adverse impacts to the lake's fish composition or standing crop. Rotenone sampling in McGuire's discharge area indicated a similar fish stock in May 1990 as in previous years, followed by a decline to a record low of 14 kg/ha in August 1990. Hydroacoustic density estimates confirmed that limnetic fish species avoided the discharge area when temperatures exceeded 30 C. Vertical distribution of fish also reflected a response to temperature' profiles, with fish moving deeper as surface temperatures increased, and later redistributing as waters cooled. Although temperature and dissolved oxygen conditions in the summer of 1990 were deemed unsuitable for adult striped bass, no mortalities were observed or reported. iii
l l
- 11. McGUlRE NUCLEAR STATION OPERATIONAL DATA OPEFATIONAL CllAftACTERISTICS--1990 The 1990 annual mean capacity factor (CF) was 56.6% for McGuire Nuclear Station (MNS). 47.6% for Unit 1. and 65.6% for Jnit 2 (Table 1). Both units were operational during July and August and only Unit I during September, when discharge temperatures are most critical.
During these three months the thermal limit for MNS increases from a monthly average of 95 E to 99 F. The average monthly discharge temperature was 96.9 E for July. 96.5'I for August, and 92.5 P for September 1990. Use of low level intake water was not necessary for compliance with the new thermal limit for MNS. This helped to conserve habitat for cool water f ish in Lake Norman. Other than a test of low level intake pump operability in September, use of low level intake water to improve the efficiency of MNS was postponed until October 1990 (Figure 1). The volume of cool water in Lake Norman is tracked throughout the year to ensure that an adequate volume of cool water is available to comply with both the NRC Technical Specification requirements and the NPDES monthly discharge water temperature Jimit. I 1 t
l Table 1. Average monthly capacity factors (%) calculated from daily unit capacity factors (Net Generation (mw per unit day) x 100 / 24 h per day x 1129 mw per unit) for McGuire Nuclear Station during 1990. , Month Unit 1 Unit 2 Station Average Average Average January 23.1 102.0 62.5 February 0.0 98.9 49.5 March 0.0 99.7 49.8 April 0.0 102.2 51.1 May 16.4 99.1 57.3 June 84.6 97.7 91.2 July 96.1 98.6 97.4 August 79.4 89.3 84.4 September 85.7 0.0 42.9 October 39.9 0.0 20.0 November 45.4 0.0 22.7 December 100.2 0.0 50.1 Annual Average 47.6 f.S . 6 56.6 2 __i_._________________ _ __
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+ RUsNSNGMONTit_Y AVG TERMAL LIMIT a ROW Figure 1. The running rnonthly average (plus) conds iser cooling water discharge temperature, discharge thermal :
limit ( ), and the low-level intake flow (triangle) for McGuire Nuclear Station. l i
111. TEMPERATURE AND OlSSOLVED OXYGEN INTRODUCTION The objectives of the temperature and dissolved oxygen ID0) portion of the McGuire Nuclear Station (MNS) NPDES Maintenance Monitoring Program are to:
- 1) maintain continuity in Lake Norman's temperature and D0 data base so as to allow detection of any significant station-induced and/or natural change in the physicochemical structure of the lake; and
- 2) compare, where appropriate, these physicochemical data to similar data in other hydropower reservoirs and cooling impoundments in the Southeast.
This year's report focuses primarily on 1989 and 1990, with the specific objective of assessing the impact of raising the summer (July-September) discharge temperature at MNS from 95* F (1989) to 99* F (1990) on the lake-wide thermal and D0 structure of Lake Norman. Specific areas of investigation covered in this chapter include thermal plume validation and assessment, striped bass habitat, and reservoir-wide temperature and 00 information. Where appropriate, reference to pre-1989 data will be made by citing reports previously submitted to the North Carolina Department of Environment, Health, and Natural Resources (NCDEHNR). METHODS AND MATERIALS Water temperature and D0 were measured monthly at 12 locations (Locations 1, 5, 8, 9.5, 11, 13, 15, 15.9, 62, 69, 72, and 80; Figure 1) throughout Lake Norman in 1990 using a Hydrolab Datasonde (Hydrolab Corporation, > 1986). Additional measurements were taken at these locations at weekly to biweekly intervals during the summer to more accurately define the distribution and rate of decline of striped bass habitat. Measurements of temperature and 00 were taken at 1-m intervals throughout the water column at each location extending from the surface (0.3 m) to 1 m above the lake bottom. Calibration of the instrument followed procedures recommended by the manufacturer (Hydrolab Corporation,1986) and was performed before and after each data collection neriod. 4
The relationship between heating and cooling of lakes can be examined by comparing lake temperatures with the equilibrium temperature. The equilibrium temperature is defined as that temperature, under extant meteorological conditions, at which the net rate of heat exchange with the atmosphere would be zero (Edinger et al.,1974). Expressed in another
. way, the equilibrium temperature represents the theoretical temperature that the water body would attain, under a specific combination of meteorological conditions (air temperature, wind speed, dew point), given sufficient time. In this study, Ryan unheated equilibrium temperatures were calculated for 1988,1989, and 1990, according to Ryan and Harleman (1973), and used to assess the influence of meteorology on reservoir heat flux.
Data were analyzed using two approaches, both of which were consistent with earlier studies (DPC 1985, 1987, 1988a, 1989, 1990). The first method involved partitioning the reservoir into mixing, background, and discharge zones, and making comparisons among zones and years. In this report, the discharge includes only Location 4; the mixing zone encompass-es locations 1 and 5; the background zone includes Locations 8, 11, and
- 15. The second approach emphasized a much broader lake-wide investigation and encompassed the plotting of monthly isotherms and isopleths, and summer-time striped bass habitat. Several quantitative calculations were also performed; these included the calculation of the areal hypolimnetic oxygen deficit -(AHOD), maximum whole-water column and hypolimnion heat content, mean epilimnion and hypolimnion heating rates over the stratified period, and the Birgean heat budget.
5
RESULTS AND DISCUSSION McGuire/ Marshall Plume Size Validation l Duke Power Company requested from Aero Dynamics, Corporation (1990) an aerial infrared survey of the thermal plumes at MNS and MSS during the summer of 1990. This information was used to validate plume size ] predictions at a thermal discharge of 99* F at MNS using the Massachusetts , Institute of Technology thermal model (OPC 1988b). Results of the survey are illustrated in figure 2. The 5* F (2.8* C) above background isotherm measured 730 ac at MNS and 145 ac at MSS, both of which were substantially less than the 2006 ac at MNS and 552 ac at MSS predicted under worst-case meteorology at t discharge temperature of 99* F (DPC 1988b). The observed acreage was r.lso appreciably less than that predicted under worst-case i meteorology for the 95* F discharge criteria, i.e.,1492 ac at MNS and 714 ac at MSS (DPC 1985). Similarly, the observed acreage of the 90*F (32.2*C) L;otherm was 386 ac at MNS and 69 ac at MSS. These values were significantly less than the 1452 ac at MNS and 303 ac at MSS predicted under worst-case meteorology at a discharge teyerature of 99* F. The acreages were also less than predicted under worst-case meteorological , conditions at a 95' F discharge temperature, i.e., 982 ac at MNS and 432 ac at MSS. Temperature and Dissolved Oxygen Water temperatures measured in 1990 illustrated similar temporal and spatial trends in the mixing and background zones (Figures 3 and 4). Winter water temperatures ranged from 0.l* to 3.5* C cooler throughout the water column in both zones than in 1989 (Figures 3 and 4), and were well within the historic range (DPC 1985,1987, 1988a,1989,1990) . Spring and summer water temperatures, on the other hand, were generally warmer throughout the water column in both zones in 1990 as compared to 1989 and historically, whereas fall temperatures were within the historic range. Spring water temperatures ranged from 0.l* to 3.3* C warmer than 1989 and historically, whereas summer water temperatures ranged from 0.l* to 4.l*C warmer than historic conditions with the major increases rcstrictel 6
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primarily to the metalimnion and hypolimnion, fall temperatures ranged from 0.l* to 3.l* C warmer than in 1989, but were within the historic range. These seasonal differences in water temperature among years appears to be due primarily to a combination of meteorology and increased operations at MSS. Meteorological conditions during the winter of 1989-1990 were harsher than 1988-1989, and as a result, more water column cooling occurred in the winter of 1990 than in 1989 (Table 1). Conversely, 1990 spring meteorology was warmer than 1989, resulting in a greater storage of heat at the mid and bottom depths prior to and st the early stages of lake stratification in 1990 than in 1989. The effect of this increased heat storage was then carried over into the summer period. In other words, temperatures were warmer in the mid-to-lower portions of the water column during the summer stratified period in 1990 than in 1989 because of, in part, the increased storage of ' natural' heat prior to the lake becoming strongly stratified. This explanation is supported by 1) these between-year differences were generally consistent in both the background and mixing zones, and 2) the average lake-wide metalimnion / hypolimnion heating rate in 1990 (0.077* C/ day) was slightly less than in 1989 (0.085* C/ day). A second f actor contributing in the etserved increase in summer-time temperatures in the metalimnion arid hypolimnion in 1990 over 1989 was operations at MSS. Condenser cooling water flow at MSS in 1990, over the period 1 May through 30 September, averaged 812,000 gallons / minute contrasted with 661,500 gallons / minute in 1989, or about a 23% increase. The importance of condenser cooling water flow at MSS in influencing interannual variability in the temperatures of Lake Norman was illustrated in studies by Forts (1985) and DPC (1986), f all water temperatures ranged from 0.l* to 2.5* C warmer than measured in 1989, but generally were within the historic range (Figure 3 and 4). Mild meteorological conditions also appear to explain the differences between 1989 and 1990 September through December water temperature data (Figures 3 and 4; Table 1). Discharge temperatures illustrated the same temporal trend between 1989 and 1990 as did water column temperatures, i.e., winter temperatures were ~ 7 1 1
. c slightly cooler (by 4* C), whereas spring and early-summer temperatures were slightly warmer (by 2* to 6* C) in 1990 than in 1989 (Figure 5). i Meteorology again appears to be the primary factor influencing these differences, because the 99* F variance did not take effect until July.
The warmest discharge temperature of 1990 occurred in July and measured 34.6* C (94.3* F), which was 1.9* C warmer than in 1989 and historically (DPC 198S, 1990). Seasonal and spatial patterns of D0 in 1990 were generally similar in both the mixing and background zones (Figures 6 and 7). Winter D0 values ranged from 0.! to 1.0 mg/l higher throughout the water column in both zones in 1990 than in 1989, but were well within the historic range (DPC i 1985,1987,1988a,1989,1990). These between-year differences appear to be due primarily to meteorology, with the cooler 1990 winter equilibrium ! temperatures promoting a greater degree of mixinq and reaeration than occurred in 1989. Conversely, spring and summer D0 values were generally less than observed historically, particularly in the metalimnion and hypolimnion where 00 concentrations ranged from 0.1 to 2.2 mg/l lower than observed previously. August metalimnetic 00 values were greater in 1990 than 1989 in both zones, and were similar to maximum values observed for these depths historically. The differences among 1990 and historic spring and summer D0 values are believed to be predominantly related ta the warmer than historic water temperatures measured in the spring aad summer of 1990 which, as discussed earlier, appears to be duo to a com':' nation of meteorology and operations at MSS. Warmer water column tempercu;es would decrease oxygen solubility and increase biological respiration rates, thereby reducing the available supply of D0. An aoditional contributing comnonent is the quantity of advected oxygen brought into Like Norman via upstream inputs from Lookout Shoals (Figure 1). The average summer flow-through at Lookout Shoals Hydroelectric Station in 1989 was 70.8 m'/s contrasted with only 45.5 m'/s in 1990, indicating that less oxygen was advected into Lake Norman in 1990 than in 1989. Fall and v.arly-winter D0 concentrations were generally lower than observed in 1989, but were within the historic range. Meteorology, and its subsequent impact on the timing and degree of lake turnover, is believed to be the primary factor contributing to the differences between 1990 and 1989. ~ 8
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a The seasonal pattern of D0 in 1990 at the discharge location was similar to that measured historically, with the highest values observed during the winter and lowest observed in the summer and eary-fall (Figure 5). Winter D0 values measured in 1990 were greater than in 1989 (Figure 5) but similar to historic values, whereas spring, summer, and fall values were - slightly less (by <l.0 mg/1), equal to, or slightly more (by < l.0 mg/1) than 1989, and historic data (DPC 1985, 1986, 1987, 1988a, 1989, 1990). The lowest D0 concentration measured at the discharge location in 1990 (3.9 mg/1) occurred in Oct.ober and coincided with low-level pumping at HNS. The monthly reservoir-wide temperature and dissolved oxygen data for 1990 are presented in Figures 8 and 9. For the most part, the temporal and spatial distributional patterns of both temperature and dissolved oxygen are similar to other cooling impoundments and hydropower reservoirs in the Southeast. During the winter cooling and mixing period, vertical rather than horizontal homogeneity in temperature predominated, with the shallower uplake ' riverine' zone exhibiting slightly cooler temperatures than the deeper downlake ' lacustrine' zone (Figure 8). These longitudinal differences in temperatures were clearly illustrated in January and February. The principal factors influencing this gradient in Lake Norman are thermal discharges from MSS and HNS, morphometric (depth) differences within the reservoir, and surface water inputs from the upper reaches of the reservoir. The heating period in Lake Norman generally begins in March, as more heat is gained at the water's surface than is lost at night. During the initial stages of the heating period, buoyancy forces " smooth out" the horizontal differences in temperature, thereby reducing temperature differences between up-reservoir and down-reservoir locations. Due to the vertical instability of the water column during this period, temperature increases are observed at all depths. These points are illustrated by contrasting the January and February temperature data with the March and April data (Figure 8). As solar radiation and air temperatures increase, heating occurs at a greater rate in the ur per waters than in the mid or bottom waters. l 9
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Eventually, differential heating at the surface leads to the formation of the classical epilimnion, metalimnion, and hypolimnion zones. These zones (strata) are clearly depicted in the July,1990 data (Figure 8). In contrast to most natural lakes, but not unlike many reservoirs in the Southeast, a distir,ct thermocline within the metalimnion was not observed in Lake Norman in 1990. Rather, the metalimnion was more or less continuous with respect to vertical density differences within the lower water column, and even showed signs of merging with the hypolimnion, as illustrated in the August data (figure 8), j Cooling of the water column began in early September as illustrated by ' decreases in surface temperatures compared to August data. Concurrent with decreases in surface temperatures were an increase in the depth of the epilimnion (caused by convective mixing) and a disruption of the horizontal homogeneity in epilimnion temperatures (caused by reservoir-wide differential heating and cooling, and advective inputs from up-stream). Continuation of these differential vertical and horizontal processes led to even more pronounced thermal differences within the reservoir. For example, by October the uplake riverine zone had already
' turned over', while the downlake lacustrine zone was still strongly stratified. Not until early November was Lake Norman completely mixed vertically throughout the reservoir.
Distributional patbrns of dissolved oxygen in 1990 were similar to but not identical to temperature (Figure 9), Generally, dissolved- oxygen concentrations were greatest during the winter cooling and mixing period when biological respiration was at a minimum and atmospheric reaeration was at a maximum. The highest reservoir-wide mean concentration of dissolved oxygen (11.5 mg/1) occurred in March when the reservoir exhibited a mean temperature of 10.7'c (Figure 8). Unlike the thermal regime, no major longitudinal differencca existed in dissolved oxygen within the reservoir during the winter. Not until the lake became stratified, thereby-isolating the metalimnion and hypolimnion from ' atmospheric reaeration, were uplake-to-downlake gradients in dissolved oxygen observed. Longitudinal gradients in metalimnetic and hypolimnetic dissolved oxygen in 1990 were first observed in May. Differential s 10
i i dissolved oxygen depletion and eventual anuxic were first observed in the transitional zone (Locations 15 through 62) where hypolimnetic volume is small, water column and sediment organic matter high, and advective mixing minimal. By August, the complete hypolimnion throughout the reservoir below elevation 217 m was anoxic. This represents approximately 18% of the entire volume of the lake at full pond. Reaeration of the water column started in September concomitantly with the cooling and mixing of the reservoir. Decreasing air temperatures cooled the surface waters resulting in a convective deepening, aided by wind- ' induced mixing, of the epilimnion. As the oxygenated epilimnion eroded progressively deeper into the water column, the width of the anoxic zone decreased. Longitudinal differences in reaeration were also observed and apparently were related to differential mixing caused by HNS and MSS, upstream advective inputs, and horizontal gradients in photosynthesis (Chapter IV). Reaeration of the reservoir was essentially complete by early November, except for the bottom waters in the downlake " lacustrine" zone. Table 2 presents some common quantitative limnological calculations for the thermal environment in Lake Norman. Few comparable calculations exist in the literature for reservoirs, but these data are generally within the "ballpark" of those presented by Hutchinson (1957) for natural lakes at similar latitudes throughout the world. Table 3 presents the 1990 AH00 for Lake Norman compared to similar estimates for 18 TVA reservoirs. The data illustrate that Lake Norman exhibits an AHOD that is similar to other Southeastern reservoirs of comparable depth, chlorophyll I status, and secchi depth. f 11
4 Striped Bass Habitat Suitable pelagic habitat for adult striped bass, defined as that layer of water with temperatures s 26* C and 00 levels 2 2.0 mg/1, existed in all months in Lake Norman in 1990 except in late-July and most of August (Figure 10). The pattern and degree of habitat reduction in 1990 was similar to historic conditions; it is also typical of striped bass habitat distribution and reduction patterns in many other Southeastern reservoirs (Coutant1985). Despite habitat elimination in most of the reservoir for a period ranging from about two to four weeks in 1990, no mortalities of striped bass were reported by local fishermen or observed during weekly habitat searches conducted by DPC personnel in July, August, and September. FUTURE STUDIES No changes are planned for the Temperature and Dissolved Oxygen portion of the Lake Norman maintenance monitoring program during 1991.
SUMMARY
The reservoir-wide physicochemical structure of Lake Norman in 1990 was studied using several techniques. Aerial infrared imagery illustrated that, at a summer discharge temperature of 99* F at MNS, the size of both the 5* F above background and the 90* F isotherm plumes were substantially less than predicted by mathematical modeling using worst-case meteorological inputs. The observed acreages were also appreciably less than predicted under worst-case meteorological conditions at a discharge temperature of 95* f. Temporal and spatial trends in water temperature and 00 data collected monthly in 1990 were similar to those observed historically. Winter and fall temperature and 00 data were generally within the range of previously measured values, whereas spring tad summer temperatures ranged from 0.l* to 4.l* C warmer than historic values. These differences among years-appeared to be related primarily to a combination of meteorology and 12 r
l steam-electric operations. Similarly, spring and summer D0 values ranged from 0.1 to 2.2 mg/l lower than observed historically. Dissolved oxygen differences among years were attributed to 1) a decrease in oxygen solubility and an increase in biological respiration rates due to warmer water temperatures, and 2) a reduction in the quantity of oxygen brought into Lake Norman via upstream inputs from lookout Shoals. Reservoir-wide isotherm and isopleth information for 1990, coupled with heat content and hypolimnetic oxygen data, illustrated that Lake Norman exhibited thermal and oxygen dynamics similar to other Southeastern reservoirs of comparable size and trophic status. Suitable pelagic habitat for adult striped bass existed in all months in Lake Norman in 1990 except in late-July and most of August. The pattern and degree of habitat reduction in 1990 was similar to historic conditions; it was also typical of striped bass habitat distribution and reduction patterns observed in other Southeastern reservoirs. Despite habitat elimination in the reservoir for a period ranging from two to four weeks in 1990, no mortalities of striped bass were observed or reported. l 13
LITERATURE CITED Aero Dynamir.s, Corporation. 1990. An aerial infrared survey of Lake Norman. Charlotte, NC. Sp. Coutant, C. C. 1985. Striped bass, temperature, and dissolved oxygen: a speculative hypothesis for environmental risk. Trans. Amer. Fisher. Soc. 114:31-61. Duke Power Company. 1985. McGuire Nuclear Station, 316(a) Demonstration. Duke Power Company, Charlotte, NC. Duke Power Company. 1986. Lake Norman hypolimnetic water utilization study. DPC. Charlotte, NC Duke Power Company.1987. Lake Norman maintenance monitoring program: 1986 summary. Duke Power Company.198Ba. Lake Norman maintenance monitoring program: 1987 summary. Duke Power Company. 1988b Mathematical modeling of McGuire Nuclear Station thermal discharges. Duke Power Company, Charlotte, NC. Duke Power Company 1989. Lake Norman maintenance monitoring program: 1988 summary. Duke Power Company.1990. Lake Norman maintenance monitoring program: 1989 summary. Edinger, J. E., D. K. Brady, and J. C. Geyer, 1974. Natural water temperature responses, p. 17-26. In-Heat Exchange and Transport in the Environment. RP 49 Report No. 14. EPRI, John Hopkins Univ, Baltimore, MD.125p. I 14
_ _ - _ . - - _. = - - - . - _ _ - . _ - _ _ _ Foris, W.J.1985. Factors influencing temperature and disolved oxygen in Lake Norman and other Southeastern reserviors: thermal pollution and multiple-use management implications. DPC, Charlotte, NC Higgins, J. M. and B. R. Kim. 1981. Phosphorus retention models for Tennessee Valley Authority reservoirs. Water Resour. Res.,17:571-576. Higgins, J. M. , W. L. Poppe, and M. L. Iwanski .1981. Eutrophication analysis of TVA reservoirs in: Surface Water impoundments. H. G. Stefan, Ed. Am. Soc. Civ. Eng., NY, pp.404-412. Hutchinson, G. E.1957. A Treatise on Limnology, Volume 1. Geography, Physics and Chemistry. John Wiley & Sons, NY. Hydrolab Corporation. 1986. Instructions for operating the Hydrolab Surveyor Datasonde. Austin, TX. 105p. Ryan, P. J. and D. F. R. Harleman.1973. Analytical and experimental study of transient cooling pond behavior. Report No. 161. Ralph M. Parsons Lab for Water Resources and Hydrodynamics, Massachusetts Institute of Technology, Cambridge, MA. 15
Table 1. Monthly average equilibrium temperatures (*C) for the Lake Norman watershed in 1988, 1989, and 1990. i 110.6 1M 191Q January 1.0 6.6 7.5 February 6.7 7.5 10.7 March 13.0 12.9 14.2 Aprt' 17.2 18.3 18.5 May 24.1 22.0 22.6 June 27.5 27.9 27.5 July 29.3 28.6 28.3 August 29.2 27.5 28.5 September 23.3 23.4 24.7 October 13.8 17.9 18.7 , l November 10.7 10.7 12.5 December 4.8 0.5 7.7 l Table 2. Heat content calculations for the thermal regime in Lake Norman in 1990 Maximum areal heat content 28,306 g. cal.cm d d Maximum hypolimnetic (below 11.5 m) areal heat content 15,672 g. cal.cm Birgean heat budget 19,594 g. cal.cm d Epilimnion (above 11.5 m) heating rate 0.095* C day Hypolimnion (below 11.5 m) heating rate 0.077* C. day' 16
1 t Table 3. A comparison of- areal hypolianetic oxygen deficits (AH00), summer chlorophyll i l a (chi a),. secchi depth (SD), and mean depths ,,of Lake Norman and 18 TVA reservoirs.
- i
~
j AH00~ Summer Chi a Secchi Depth Mean :
- 4. o Reservoir. . (og cm '. day _1) (vg-L-1) (m) Depth (m) I i
Lake Norman. 0.056 5'. 0 3.0 10.25 l -TVA* { Mainstem i i- Kentucky 0.012 9.1 1.0 5.0 - Pickwick 0.010 3.9 0.9 6.5 !
- Wilson 0.028 5.9 1.4 12.3
i Wheelee 0.012 4.4 - 5.3 i Guntersv111e 0.007- 4.8 1.1 5.3 ! i N Nickajack 0.016 2.8 1.1 6.8 r I Chickamauga 0.008 3.0 1.1 5.0 l Watts Bar 0.012 6.2 1.0 7.3 ! Fort London 0.023 5.9 0.9 7.3 l i i Tributary j
- Chatuge 0.041 5.5 2.7 9.5 t l Cherokee .O.078 ,
10.9 1.7 13.9 !- Dougias 0.046 6.3 1.6 10.7 Fontana 0.113- 4.1 2.6 37.8 F Hiwassee 0.061 5.0 2.4 20.2 Norris 0.058 2.1 3.9 16.3 l South Holston 0.970 6.5 2.6 23.4 ; i Ties Ford 0.059 6.1 2.4 14.9 ' Watauga 0.066 2.9 2.7 24.5 ! i I
- Data taken from Higgins et al. (1980), and Higgins and Kim (1981) !
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IV. WATER CHEMISTRY INTRODUCTION The objectives of the Water Chemistry portion of the McGuire Nuclear Station NPDES Long-term Maintenance Program are to:
- 1) maintain continuity within Lake Norman's historic w>tter chemistry data base at " critical" lccations;
- 2) detect any significant impacts from Duke's operations;
- 3) document any long-term natural changes in the chemistry of the lake, which might affect plant operations;
- 4) compare, where appropriate, these data to other impoundments in the Southeast.
This year's report focuses on water chemistry in the McGuire Nuclear Station (MNS) discharge (Location 4.0), mixing zone (Locations 1.0, 2.0, and 5.0), and mid-lake background zone (Locations 8.0 and 11.0) during 1989-90 (Figure 1, Chapter III). This report particularly addresses any changes in the water chemistry that can be related to an increase in the MNS thermal discharge limit from 95 F (summer 1989) to 99 F (summer 1990). Any reference to c.arlier historical data will cite Duke Power reports previously submitted to the North Carolina Department of Environment, Health, and Natural Resources (NCDEHNR). I METHODS AND MATERIALS All monitoring locations are depicted in Figure 1 (Chapter III). Physical and chemical water quality parameters, sample locations, and collection frequencies are denoted in Table 1. Water chemistry collection methods have been previously described (Duke Power Co. 1989). Chemical enalytical methods are listed in Table 2. During 1990, potassium was analyzed by atomic adsorption graphite furnace direct injection, and the detection limit was lowered to 0.1 mg/1. 37 _.______L__________
RESULTS AND DISCUSSION precipitation Amount During 1990, about 47 inches of precipitation fell in the vicinity of MNS, compared to 52 inches during 1989 (Figure 1). The wettest month of 1990 was October, in which 27% (12.5 in.) of the annual precipitation fell. annual precipitation during both years was relatively hish for the fifteen-year period. Turbidity and Specific conductance Annual mean turbidjty values near the surface were low (2-4 NTU) at the MNS discharge, mixing zone, and mid-lake background locations during 1989 and 1990 (Table 3). Annual mean turbidity near-bottom ranged from 7 to 24 NTU over the two-year period, well within the range of values previously reported (Duke Power Co. 1989). The higher annual mean bottom turbidities in 1990 compared to 1989 are probably related to rainfall, lt is presumed that suspended sedLnents in runoff following precipitation events in May and October had settled to the near-bottom strata of the lake when samples were collected in May and November. Annual mean specific conductance (surface and bottom) in the MNS discharge, mixing, and mid-lake background zones decreased about 18% (10-16 umho/cm) from 1989 to 1990, which was attributed to a Oscrease in the dissolved ions, sodium and. chloride (Table 3). The 1990-annual means ranged from 56 to 61 umho/cm. Specific conductance values were similar (within 4 umho/cm) among the discharge, mixing zone, and mid-lake background zones in 1990. pH and Alkalinity During 1990,-annual mean pH and alkalinity values were similar among l MNS discharge, mixing, and mid-lake background-zones (Table 3). Annual mean pH and alkalinity for each location were consistently lower (0.2-0.5 pH units and 2-3 mg CACO 3
/l) in 1990 than in 1989.
38
1'
-Quarterly p: .nd alkalinity values at all locations for both years were within their historical ranges (Duke Power Co. 1989).
Major Cations and Anions The concentrations (mg/1) of major lonic species in the MNS discharge, mixing, and mid-lake background zones are provided in , Table 3. The overall ionic composition of Lake Norman during 1990 was similar to that-reported for 1988 and 1989 (Duke Power Co. 1989, 1990). The major cations (descending order as equivalents /1) were , l sodium, calcium, magnesium, and potassium; major anions (descending i order as equivalents /1) were bicarbonate (the primary component of alkalinity), sulfate and chloride. Annual means of sodium and ) chloride concentrations during 1990 were similar among the lake zones (Table 3), and were 2-3 mg/l lower that, the 1989 annual means, j 1 The decrease in sodium and chloride concentrations appeared unrelated to MNS-operations and/or rainfall. Nutrients Nutrient levels in the discharge, mixing, and mid-lake background zones of Lake Norman are provided in Table 3 (p. 4 of 4). Nitrogen and phosphorus levels during 1989-90 were within the ranges historically reported (Duke Power Co. 1989), and are characteristic of the lake's oligo-mesotrophic status (Rodriguez 1982). .The slightly higher annual mean concentrations of nitrite + nitrate _from all three lake-zones _for 1990 compared to 1989 were attributed to the relatively higher inputs during'the winter and spring of 1990. Ammonia nitrogen concentrations increased-in bottom waters of the MNS discharge, mixing, and mid-lake ~ background zones during the= summer and fall of 1989-90. Phosphorus concentrations were generally-similar or slightly less in 1990 than.in 1989, which is _ partly explained by the lowered analytical detection limits in 1990. Metals Metal concentrations in the discharge, mixing, and mid-lake background zones of Lake Norman during 1989-90 (Table 3) were within their historical ranges (Duke Power Co. 1989). 39
.-- ..w.- -,.I--
Iron concentrations near the surface were generally low (1 0.1 - 0.2 mg/i) during 1989-90. Iron levels near the bottom where higher during the summers of 1989 and 1990, when bottom waters were anoxic. The release of iron from Lottom sediments during summer anoxia was sufficient to erceed the NC water quality standard (1 mg/1) at mixing and background zone locations during the summer of both years. Similarly, manganese concentrations in near-surface and near-bottom waters were generally low (f 0.12 mg/l) during 1989-90, except during the summer / fall of both years when bottom waters approached or became anoxic (Table 3). Manganest concentrations near the bottom rose above the NC water quality standard (0.5 mg/1) at mixing zone and background zone locations during the summer and fall of both years. Heavy metal concentrations in Lake Norman never approached NC water quality standards, and there were no consistent appreciable differences between the two years. FUTURE STUDIES The following changes to the Water Chemistry component of the McGuire NPDES Lake Norman Long-term Maintenance Program were approvad by the NCDEHNR beginning March, 1991:
- 1. Elimination of water quality sampling at Location 1.2. _
Currently only surface data are collected at this location. Data collected at Locations 1.0 and 2.0 are indicative of conditions at the MNS intake.
- 2. Discontinue the analysis of soluble elements at Location 2.0. The historical data base on Lake Norman is adequate to address differences in soluble (0.45 um filtered) and unfiltered elements in Lake Norman.
- 3. Elimination of fluoride analyses. Fluoride is not an important ionic component of Lake Norman. Also, fluoride concentration is well under NC water quality standards and is too low to impact ion mass balance concentrations 40
a in the lake.
- 4. Reduce sampling at Location 16.0 from quarterly to nomi-annually, which is consistent wit h the sampling frequency for all other Mountain Island reservoir locations.
SUMMARY
All water chemistry parameters were within the historical ranges previously reported for the lake during both MNS preoperational and operational years. The operation of MNS under a 99 F summer thermal discharge limit during 1990 had no apparent irnpact on the water chemistry. LITERATURE CITED Duke Power Company. 1989. Lake Norman maintenance program: 1988 cummary. Water chemistry chapter. pp. 6-65. Duke Power Company. 1990. Lake Norman 1989 summary-- maintenance rnonitoring program McGuire Nuclear Station: HPDES No. NC0024392. pp. 5-56. 41
iiclear ion McGuire M0nthly Rainfcll Totals ByYeer 34 o .. 12.0 -- 10.0 -- 50 -- h e 6.0 -- - 4.0 -- 20 N Joa FC D Ih, Ar 0 Woy Jun M Asg 5,g Oct h g gy E 1989 [] 1990 MCGUIRE YEARLY RAINFALL TOTALS so.o . --
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Table 2. Water chemistry methods and analyte detection limits for the McGuire Nuclear Station NPDES
. long-term maintenance monitoring program for Lake Norman.
Pr m r m i.pn Detection Limit Method Img-CACO,-1-**
- _____Y a r i.AhltL **C Alkalinity, total Electrometric titration to a pH of 5.18 0.3 mg 1
- 0.5% HNO, Atomic emission /1CP-direct injectind 0 050 m-gl '
Aluminum 4*C Ammonium Automated phenate' 0.1 vg 1-* 8 0. 5* 5+NO, Atomic absorption / graphite furnace-direct injection 0.04 mg-1-' Cadmium O. 5* WO, Atomic emission /ICP-direct injection' 1.0 mg-1-' Calcium 4*C Automated ferricyanide' 1 vaho cm '* Chloride In-situ Conductance, specific Temperature compensated nic6*I electrode' 0.5 og 1
- O.5% WO, Copper Atomic absorption / graphite furnace-direct injectior' 0.10mg.1-'
4*C fluoride Potentiometric' O . 5*. HNO, 0.1 mg 1~' Atomic emission /ICP-direct injection' 1-' Iron 2 0. 5*. PNG, 2.0 og Atomic absorption graphite furnace-direct injection 0.001 mg 1 8 leed 0.5% HNO, Atomic emission /ICP-direct injection
- 0. 00 3 mg- 1 '
- Magnesium O.5% HNO, Atomic emissien/1CP-direct injection' 0.050 mg 1"'
w Manganese 4*C u Nitrite + Nitrate Automated cadstum reduction' 0.005 mg 1-* 4*C Orthophosphate Automated ascorbic acic reduction, 0.1 ma-I ** In-sit.u Temperature compensated polavographic cell 2 Onygen, dissolved In-situ 0.1 std. units' Temperature compensated glass electrode' 0.005 eg- 1 '" cH 4*C Phosphorus, total Persulfate digestion followed by automated ascorbic acid O . 015 og 1 - '" reduc t i on ' 0.1 mg 1 O.5% HNO, Atomic absorption graphite furnace-direct injection' Potassium 4*C 0.5 mg 1 Automated molydosilicate' 0. 3 m gl-' Silica 8 0.5% HNO, Atomic emission /ICP-direct injection 1.0 mg 1 ' Sodium 4*C Turbidimetric. using a spectrophotometer' Sulfate In-situ D.1*C* Temperature Thermistor / thermometer
- 1 NTU" 4*C Turbidity Nephalometric turbidity
- 4 .g-1 O.5% HN0, Atomic emission /ICP-direct injection' Zint Methods for chemical analysis of water and wastes.
' United States Environmental Protection Agency 1979.
Environmental Monitering and Support Laboratery. Cincicnati. 0$1.
'U$ EPA. 1982.
'USEPA. 1984 . J
- Instrument sensitivity used instead of detection limit. I "Detec t i on Itmit changed during 1989
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ftble 3. Quarterly near-surface (0.3a) and near botton (botton sinus Is) water chemistry for the MNS discharge, mixing zone, and backgrond locations on Larce Norman during 1989 and 1990. The symbol. "<". denctes a value less than the azalytical detection limit. Yalnes less than detection were assumed to be the detection - limit for calculating a mean. Mixing Zone Mixing Zone MNS Discharge Mixing Zone Backgrond lackgrouct LOCATION: 1.0 2.0 4.0 5.0 8.0 11.0 DEPTH: Surface Bottca Surface Botton Surface Surface Bctton Surface Botton Sarface Bottes FARAXETERS YEAR: '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 '89 '90 Turbidity (atu) Feb 2 4 11 6 2 3 5 6 2 4 2 4 2 6 2 4 7 4 2 5 11 9 May 2 3 3 14 2 3 3 12 2 3 2 3 4 12 2 3 3 13 2 3 4 19 Aug NA I NA 7 NA 1 NA 12 NA 1 NA 1 NA 11 NA 1 NA If NA 2 NA 11 Nov 3 3 10 18 2 4 9 20 4 5 3 3 11 7 4 5 9 22 3 6 24 _22 Annual Mean 2 3 8 11 2 3 6 12 3 3 2 3 6 9 3 3 6 13 2 4 13 15 Specific condsctance (uth7/ca) Jan/Feb 69 59 69 57 NA 59 NA 57 NA 60 6E 59 69 SE 68 59 6E 56 76 56 73 55 May 77 51 79 53 77 51 79 53 7E 52 77 52 75 52 79 51 El 51 80 48 82 50 Aug 63 58 78 68 64 59 80 7C 64 59 64 59 80 75 64 SE 78 68 63 59 79 70 Nov 63 59 64 56 63 59 60 55 61 SE 62 SE SE 59 62 59 64 54 59 61 51 53 Annual Mean 64 57 73 SE 6E 57 73 59 6E 57 6e 57 71 61 66 57 73 57 70 56 71 57 pE (nnits) Feb 7.0 6.E 6.E 6.7 7.0 6.8 6.E 6.6 6.5 6.7 7.1 6.E 6.9 6.6 7.1 6.5 6.E 6.7 7.2 6.8 6.8 6.6 May 7.5 6.9 7.0 6.4 7.6 7.1 7.0 6.4 7.2 6.6 7. 4 6.9 7.0 6.4 7.6 6.e 6.9 6.3 7.5 6.9 6.8 e.2 Aig 6.6 6.5 6.4 6.3 6.5 6.5 6.5 6.4 6.4 6.3 6.5 6.5 6.3 6.2 7.2 t.6 6.4 c.4 7.8 6.7 6.5 6.4 N Nov 6J L7 6.2 62 1 6.E 6.2 6.5 6,4 6.6 6.7 6.E 69m 631 tc. 5 6.8 6,7 6.7 6.1 6J 6,8 6,2 62 m Annual Meat 7.0 6.7 6.6 6.4 7.0 6.8 6.7 6.5 6.6 6.6 7.0 6.E b.6 6.4 7.2 t.8 6.7 6.4 7.3 6.8 6.6 6.4 Alkalinity (a; CACO./l) Feb 14 11 14 11 14 11 14 11 14 11 14 11 14 11 14 11 14 11 14 11 15 11 May 14 11 14 11 14 11 14 11 14 11 14 11 14 11 14 11 14 10 14 10 14 10 Ane 14 12 16 15 14 12 19 16 14 12 14 12 20 18 14 12 20 18 15 12 17 17 Nov 12 13 13 11 13 13 12 11 13 13 13 13 12 13 13 12 13 10 12 12 11 10 Annual Mean 14 12 14 12 14 12 15 12 14 12 14 12 15 13 14 12 15 12 14 11 14 12 i Chloride (ag/1) Feb 7.4 4.8 7.4 4.7 7.4 4.8 7.5 4.6 8.8 4.9 7.5 4.8 7.4 4.7 7.1 4.1 7.9 4.5 7.5 4.3 9.4 4.4 May 7.5 4.1 7.9 4.3 7.7 4.2 8.1 4.4 8.0 4.3 7.7 4.3 7. 8 4.4 7.7 4.2 8.0 4.1 8.0 3.9 8. 5 4.0 Aug 7.4 4.1 7.8 3.9 7.2 4.1 7.9 4.4 7.0 4.4 7.2 4.8 7.5 4.5 7.1 4.6 7.6 4.7 7.9 4.6 7. 8 4.0 Nov 6.2 43 1 4.9 3c m 6.1 3,8 5.8 42 6J (J 6J (J 5J L3 6J 5.2 6.6 4.1 57 3.7 4.0 L3 l Annual Mean 7.2 4.3 7.0 4.2 7.1 4.2 7.3 4.4 7.5 4.6 7.2 4.7 7.1 4.5 7.0 4.7 7.5 4.4 7.3 4.1 7. 4 4.2 Snifate (a;/1) Feb NS MS NS NS 5,8 6.h 7.3 6.5 5.8 6.5 NS NS MS NS 5.9 6.4 5.8 6.4 NS E NS E Aug NS NS E E 71 5.0 67 7_J L8 48 NS E NS NS 7.0 5,0 L5 9.0 E E E E Annual Mean 6.5 5.7 7.0 7.0 6.3 5.6 6.5 5.7 6.7 7.7 NA = Not analyzed NS = Not sampled i e
Fage 2 of 4 Table 3. (Continued) Backgrond Ba-Jgrond MNS Discharge Mixing Zone 11.0 Mixing Zone 5.0 8.0 Mixing Zone 4.0 Botton Surface Botten 1.0 2.0 Surface Ection Sarface '89 LOCATION: Ectton Surface '90 '89 '90 '89 '90 '90 Botton Surface '89 '90 '89 '90 '89 DEPTH: Sarface
'90 '89 '90 '89 '90
'89 '90 '89 '90 '89 PARAMETERS TEAE:
2.7 3.0 2.7 2.9 2.7 3.0 2.7 3.0 2.6 2.9 3.0 Calclua (ag/1) 3.0 2.6 3.0 2.5 2.9 3.0 2.6 3.1 2.5 3.0 2.6 3.0 2.7 3.0 2.6 3.0 2.7 3.1 3.0 2.6 2.9 3.0 3.0 2.5 2.9 2.7 3.2 2.8 2.5 3.4 3.1 Feb 2.6 2.9 2,8 3.1 4.1 3.1 3.3 2.6 3.3 2.9 2.6 3.0 2.9 2.6 3.5 2.6 25 2J 25 2J I4 May 4.0 3.0 3.4 2.6 3.8 3.0 2.7 25 2J 2J 26 2J 2.8 Aug 3.0 2.6 2J 2.8 2J 2J 2J 2J 1 2.6 3.0 2.8 2.9 2.6 3.0 2J 2J 2J 25 2J 2.8 2.9 2.6 3.0 2.6 3.2 2.6 3.0 Nov 2.6 3.0 2.6 3.2 Annual Mean 2.9 2.6 3.2 1.2 1.4 1.2 1.3 1.1 1.4 1.2 1.4 1.2 1.4 1.4 1.2 1.4 1.2 1.2 1.3 1.1 1. 3 1.3 Magnestur (ag/1) 1.1 1.4 1.2 1.4 1.2 1.4 1.1 1.3 1.2 1.3 1.4 1.2 1.4 1.3 1.1 1.3 1.2 1.3 1.3 1.2 1.4 1.3 Feb 1.1 1.3 1.2 1.4 1.3 1.3 1.5 1.2 1.4
.3 1.1 1.3 1.4 1.2 1.6 1.2 1.7 IJ IJ L1 May 1.3 1.5 1.2 1.6 1.2 L2 1.3 1.3 1.2 1.3 L1 IJ 1.2 Aug 1.4 1.2 1.7 1.2 1.3 1.1 1.3 IJ IJ L2 1.2 1.4 1.2 1.3 1.2 1.3 l3 1.4 1.2 1.4 Nov L3 L3 L3 IJ 1.2 1.4 1.2 1.4 1.2 1.4 1.2 1.4 1.2 1.4 1.1 1.4 Ann al heat 1.6 1.5 1.6 2.C 1.4 2.0 1.7 1.9 1.7 1.9 1.7 2.0 1.7 2.1 1.7 1.5 NA 1.3 NA 1.5 Potas:iu (na/1) 1.6 1.7 1.5 1.E 5.1 2.0 1.5 NA 1.5 NA 1.5 NA 1.7 1.7 Feb 1.7 1.7 N' 1.4 NA 1.8 1.5 1.5 1.7 1.7 1.5 1.6 NA 2.0 1.8 1.9 NA 1.6 NA NA 1.9 1.E 1., 1.8 1.9 1.7 1.9 1.E 2.2 1.8 2.0 1.7 2J May 1.7 2.0 1.6 1.9 1.7 JJ IJ 1.7 1.8 1.6 1.8 1.7 1.8 1,9 L2 1.8 IJ IJ 1.8 1.8 1.8 Aug I
J L7 1.9 2J IJ JJ 1.8 1.6 1.9 1.6 1.9 1.7 1.9 1.7 u Nov 1.8 2.5 1.9 1.8
- Anual Hean 1.8 1.6 '.9 2.0 4.8 7.5 4.8 9.6 4.4 7.2 5.0 7.1 5.1 7.5 7.3 5.1 7.2 5.1 4.3 8.0 3.8 8.2 4.1 Sodin (ag/1) 4.7 7.1 4.7 6.6 4.8 8.1 4.3 8.2 4.3 S.2 3.9 7.0 5.0 7.3 4.8 8.2 4.0 8.1 4.3 7.7 4.0 7.1 4.2 7.9 Feb 4.2 8.0 4.5 8.5 8.8 4.0 8.4 4.2 May 8.1 4.3 8.3 4.1 8.7 3.9 7.5 4.1 8.6 4.2 6,2 5.6 6J L3 5.6 5.8 4.1 4J 4.0 9.2 4.0 8.4 LO 5_J 4,3 4.6 7.5 4.2 7.7 5.8 (J L8 5.0 5_J 4.5 7.4 4.3 7.1 Aug 4.5 6.2 5.0 4.6 7.3 4.5 7.5 Nov 61 5,2 L8 4.6 7.9 4.5 7.2 4.5 7.4 4.6 7.4 4.3 7.4 Annual Mean 7.2 NA = Not analyzed MS = Not sampled
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V. PHYTOPLANKTON INTRODUCTION Phytoplankton population parameters were monitored in 1990 in accordance with the NPDES permit for McGuire Nuclear Station. The objectives of the phytoplankton section for the Lake Norman Maintenance Monitoring Program are to:
- 1. Describe quarterly patterns of phytoplankton standing crop and species composition throughout Lake Norman, and
- 2. Compare phytoplankton data collected during this study (February, May, August, November 1990) with historical data collected during these months.
Previous studies on Lake Norman have reported considerable spatial and temporal variability in phytoplankton standing crops and taxonomic composition (Duke Power Company 1976, 1985; Menhinick and Jensen 1974; Rodriguez 1982). Rodriguez (1982) classified the lake as oligo-mesotrophic based on phytoplankton abundance, distribution, and taxonomic composition. METHODS AND MATERIALS Quarterly phytoplankton sampling was conducted at Locations 2.0, 5.0, 8.0, 9.5, 11.0, 13.0, 15.9, and 69.0 (Chapter 111, Figure 1). Duplicate composite grabs from 0.3, 4.0, and 8.0 m (i.e., the euphotic zone) were taken et all locations. Sampling was conducted on 28 February, 24 May, 30 August, and 2 November 1990. Standing crop (density and biovolume) and taxonomic composition were determined for samples collected at locations 2.0, 5.0, 9.5, 11.0, and 15.9; chlorophyll a concentrations and seston dry and ash-free dry weights were determined for samples from all locations. Field . pling methods, and laboratory methods used for chlorophyll a, seston weights, standing crop, and taxonomic composition determinations were identical to those used by Rodriguez (1982). Data collected in 1990 were compared with corresponding data from quarterly monitoring beginning in August 1987. 49 t
RESULTS AND DISCUSSION jtandina (r.pg j Standing crop values for phytoplankton were generally highest at mid and uplake Locations 11.0, 13.0, 15.9 and 69.0 (Figure 1). All chlorophyll A values above 10 mg/m2 were found uplake, including the highest value observed ; during 1990, 15.1 mg/mi at Location 15.9 in February. By contrast, no chlorophyll a concentrations greater than 6.0 mg/mi were found at Locations 2.0, 5.0, 8.0, or 9.5 (Table 1) . Chlorophyll a concentrations varied the tocau en reb may hg uv most at Location 69.0 where the lowest 2.0 3.47 5.25 4 9s 2.ro values of any location were found in s.o 4.36 5. n 3. n 3.23 February, May, and November, but which e.o 5,,7 4.,4 4,75 3,47 exhibited the highest value in August 9.5 5.25 4.9 s.04 4.40 (10.6 mg/mi) . This August peak in u.o 7.54 4.9 s.9 4.s chlorophn 1 A at Location 69.0 was also n.o 10.n s.13 3.1s 3.o observed in 1988 and 1969 (Figure 2). 3,, g , ,, 3, g 3,g ,,,3 The yearly hight for both total g,, ,,,3 ,,g 373, 3,33 densities and biovolumes were also observed uplake: at location 11.0 in February for biovolumes (2,244 mm2/m>) and at Location 15.9 in August for densities (3,973 units /ml). Total phytoplankton-densities at Location 15.9 were consistently higher than at any other location during every month sampled since August 1987, except February 1990, and also peaked in August (Figure 3). This trend of increased standing crop values from downlake to uplake has-bean observed in past years (DPC 1988, 1989 and 1990) and may be due to higher inputs of nutrients associated with increased suspended solids uplake as evidenced by seston ash-free dry weights (Figure 1). Phytoplankton standing crop values at all locations in 1990 were generally within the ranges of those obse ved during the same months of 1988 and 1989 (Figures 2 and 3) except for the high chlorophyll a value observed at Location 15.9 in February. Early spring peaks in phytoplankton are typically seen uplake in Lake Norman (Rodriguez 1982) so we may have sampled this year at the 50
maximum. Chlorophyll 1, total densities, and biovolumes in the mixing zone (Locations 2.0 and 5.0) were very similar to those observed in 1989. With the exception of total densities and biovolumes at location 15.9, star. ding crop values (especially chlorophyll 1) in February of 1990 were generally higher than in 1989. Community Composition Ten classes comprising 77 genera and 146 taxa of phytoplankton were identified from samples collected in Lake Norman in 1990. The distribution of species within classes was as follows: Chlorophyceae (Green algae), 63; Bacillariophyceae (Diatoms), 28; Chrysophyceae, 15; Haptophyceae and Xanthophyceae, 1 each; Cryptophyceae, 7; Myxophyceae (Blue-green algae), 16; Euglenophyceae, 4; Dinophyceae, 9; Chloromonadophyceae, 1; and 1 Unidentified taxon (Table 2). Twenty-two taxa were identified in 1990 which were not recorded in the Maintenance Monitoring Program since August 1987. However, none of these taxa was found in any abunriance and all but six of these taxa have been listed in previous studies in Lake Norman (Rodriguez 1982). Phytoplankton class composition in 1990 was similar to that found in 1989 (DPC 1990). Diatoms and cryptophytes were dominants in terms of densities at all locations during february, with green algae also being important downlake at Locations 2.0, 5.0, and 9.5 (Figure 4). Diatoms dominated the total biovolume in February, comprising more than 45% of the total biovolume at all locations and almost 80% of the biovolume at Location 11.0. Class composition in May was similar to that observed in February, with diatoms and cryptophytes generally codominant for density, and green algae and chrysophytas becoming more important at all locations. Diatoms again dominated the biovolumes in May, comprising more than 40% of the total at each of the locations. Dinophyceae were important in terms of biovolume at Locations 9.5 and 11.0 during May, in August, green algae dominated phytoplankton assemblages at all locations except Location 15.9, where blue-green algae were dominant with 36.6% of the total density. Tl.is was the only occurrence of blue-green algal dominance observed in 1990. High populations of blue-green algae were also observed at Location 15.9 during August in 1988 and 1989 (DPC 1989, 1990). Blue-greens comprised less than 5% of the total density at all other locations 51
during August of 1990. Diatoms and cryptophytes were also important numerically in August. Dinophyceae dominated the biovolume in August, comprising more than 35% of the total biovolumes at all locations and 60.3% of the biovolume at Location 9.5. In November, diatoms, green algae, and cryptophytes were codominant numerically. Diatoms dominated the biovolumes, comprising more than 40% of the total biovolume at all locations. I Major species of phytoplankton (>5% of the total density or biovolume) observed during 1990 are presented in Tables 3 and 4. Species composition among phytoplankton samples collected during 1990 was generally similar to that observed for samples collected during 1989 (DPC 1990). Rejniin ambiaua, a centrate diatom, dominated the phytoplankton biovolume at all locations during February, comprising from 17.8% of the total at location 5.0 to 65.4% of the total at Location 11.0. Melosira ambign (formerly called delelin italica) is a perenial spring dominant in Lake Norman (Rodriguez 1982). Another centric diatom, Attheva zachariasi dominated the biovolume of phytoplankton assemblages downlake during May, comprising more than 20% of the total biovolume at Locations 2.0, 5.0, and 9.5. This species appeared to take the place of Cyclotella sata, which dominated the biovolume at these same locations during May of 1989. Cyclotella s ata was not seen at all in 1990 and had not been observed in previous Lake Norman studies prior to 1989. The presence of this species in 1989 was an unusual event for which there is no ready explaination. Attheva rachariasi was also a major (>5% biovolume) species during May 1989 at most locations so its dominance in May 1990 is not unusual. Synedra spp., a pennate diatom, dominated the biovolume at Location 15.9 in May, comprising 32.2% of the total. Dinoflagellate species, primarily Peridinium spp., dominated the biovolumes at all locations during August of 1990. This was similar to 1989 except that few d,inoflagellates were found at Location 15.9 in August of 1989. In November, Melosira ambiaua w.u: again an important part of the biovol e at all locations, while Attheva zachariasi was only important downlake. Rhodomona,1 minuta, a small cryptophyte, was overall the most numerically abundant taxon in 1990, comprising from 12% to 30% of the total phytoplankton density at all locations in February, May, and November. Rhodomonas minuta has consistently been a numerical dominant in phytoplankton assemblages in 52
l l Lake Norman (Rodriguez 1982). In August, coccoid greens comprised more than 10% of the total densities at all locations and were the numerical dominant except at Location 15.9 where Banbidingtil curvala, a blue-green alga, comprised 17.3%. B turvata was also abundant at Location 15.9 in August of 1989. Other taxa comprising greater than 10% of the total densities during 1990, all commonly observed in previous studies, were inkistrodramg1 falcatus
- v. ginttilia, MicractiniWD pAlillum, Unidentified chrysophytes and (rygtgmgggy RL911 SUMHARY Phytoplankton sampling was conducted at locations 2.0, 5.0, 8.0, 9.5, 11.0, 13.0, 15.9, and 63.0 on Lake Norman in February, May, August, and November 1990. Chlorophyll a analyses and seston weights were performed at all locations, while phytoplankton standing crops and taxonomic composition were determined at locations 2.0, 5.0, 9.5, 11.0, and 15.9.
Phytoplankton standing crops (chlorophyll 1, total denstties,and biovolumes) generally showed a trend of increasing values from downlake to uplake locations. Except for chlorophyll a concentrations at location 15.9 in February, phytoplankton standing crop values during 1990 were generally within the ranges of those observed during 1987, 1988, and 1989. Phytoplankton taxonomic composition during 1990 was similar to that observed during the same t.;onths of 1989, with diatoms, green algae, chrysophytes, and cryptophytes the most abundant classes of algae observed. Diatoms generally dominated the phytoplankton biovolumes in all months but August when dinoflagellates were dominant. Blue-green algae were not an important part of the phytoplankton community except at location 15.9 in August as was also observed in 1989. Major taxa observed in 1990 were also similar to those observed in 1989. Melosira ambiava dominated the algal biovolume in February and November of 1990 and Rhodgmonas ging13 was the numerical dominant during all months but August when coccoid greens were generally most abundant. (rclotella tamtg which had dominated the biovolumes at most locations during May 1989 was replaced in May 1990 by another centric diatom Attheva tachariasi. 53
LITERATURE C11ED Duke Power Company. 1976. McGuire Nuclear Station, Units 1 and 2, Environ-mental Report, Operating License Stage. 6th rev. Volume 2. Duke Power Company, Charlotte, NC. Duke Power Company, 1985. McGuire Nuclear Station, 316(a) Demonstration. Duke Power Company, Charlotte, NC. Duke Power Company. 1908. Lake Norman maintenance monitoring program: 1987 summary. Duke Power Company. 1989. Lake Norman maintenance monitoring program: 1988 summary. Duke Power Company. 1990. Lake Norman maintenance monitoring program: 1989 summary. Henhinick, E. F. and L. D. Jensen.1974. Plankton populations, p. 120-138 h L. D. Jensen (ed.). Environmental reponses to thermal discharges from Marshall Steam Station, Lake Norman, NC. Electric Power Research Institute, Cooling Water Discharge Project (RP-49) Report No. 11. Johns Hopkins Univ., Baltimore MD. 235 p. Rodriguez, H. S. 1982. Phytoplankton, p. 154-260 h J. E. Hogan and W. D. Adair (eds.). Lake Norman summary, Technical Report DUKEPWR/82-02 Duke Power Company, Charlotte, NC. 460 p. 54
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...,\ ., # % ,, " .o v u .p . . . . >. . s x 2,000
_ %, ., .;N /, . _. , _ ,, / %m . - w ;.... ... ~.;% 0 Aug Nov I Feb May Aug Nov I Feb May Aug Nov I Feb May Aug Nov 1987 1988 1989 1990 mm3/m3 Total Blovolume 6,000 5,000 -\ li.
\ ,i \:
\ l \
A,000
-\ j \
\ :
i \: 3,000 I
\ :} \
- 4. . /\ l \
2,000 !s~ ~ I \ \
-: . Jj. Y \'\, j' , i j
\
' g. /
4 g/ .
- ..~
\ ../ s.. v y -..s.N -
1,000 -/
- i. 4- d..ss -
, s -n_~~~ . / . ., ' ~.., - 3
! i i i i i i i i i i i o ! !
Aug NovI Feb May Aug Nov I Feb May Aug Nov IFeb May Aug Nov 1987 1988 1989 1990 2.0 5.0 9.5 11.0 15.9 Figure 3. Total densities (units /ml) and total biovolume (mm'/m2) of phytoplankton in samples collected from locations in l.ake Norman, NC during quarterly sampling 1987 through 1990. 57 __._._..1..___..___.________
NO./m Density mm3/m3 Blovolume ! i.s00 - ! zu
- Mixing , , , . ,, , _
i Zone ,
'" ~
! Loc. 2 & 5 500 - F Iob May Aug Nov 0 ... Iob May Au0 Nov 1,500 - I I ! E500 - i i
~
Loc. 9.51,000 ** '" ~ W 4 i 1,000 - // '00 s -
~
Soo . 0 fob May' Aug Nov Fob May Aug Nov 4.000 zLOO 6 ._ .a l
'" ~
Loc.11.0z o . 1,000 - {=
- 1,000 -
W - 0 Feb May Aug Nov Feb May Ang Nov 1,500 - 4.000 -
- 1 -
3,000 _ 1,000 - Loc.15.9 0 fob May Aug Nov feb May Aug Nov , E DACRAA10PHYCEAE C CHLOAOIHYCEAE D CHAYSOPHYCEAE r] CRYPTOPHYCEAE j C vyxOPHYCEAE O ONOPHYCEAE O OTHER Figure 4. Class composition of phytoplankton in samples collected from locations in Lake Norman, NC during 1990. 58
Table 2. Phytoplankton taxa identified from Lake Norman samples collected in August and November 1987 and February, Hay, August, and November 1988, 1989 and 1990 (*-taxon not recorded before 1990). CHLOROPHYC[ A[ Micrattiritum ousillum f resenius Acanthosphaera Ig,hariati Lemerman Monotechidium contortum Thuret Actifiestrum bant2schii lagerheim L pusillum Priritt A41strodesmus faltatus (Corda) Ralf s M2Waeotia elemaatum ( Agardh) Vtttrock
- 8. falcatus v. mirabilis (Corda) Ralfs b e eotia m (agardh) Wittrock A. faltatus v. tumjdus (West & West) G, 5. West heobrocyt tum gjtdkiane heagelt L fusiformie Corda sensu Korshikov 3 11mneticum (G. M. Smith) G. M. Smith A. seitalis (turner) temer4 nan Detystis el1vetica v. Vest Artheodesmd in.CEg (Breb.) Hassall Q.lacustrisChodat Asterococcus limneticus G. M. Smith L Cang West & West Carteria frirschil takeda Occvstis n hergeli
(. spp. Diesing Panderina charkowiensis Korshikov Characium spp. Pediastrum Muditism Meyen Chlamydomoras spp. [hrenberg E. d ales. Meyen Chlorotonium spp. Ihrenberg E. gilyic Lucks Closterietsis jonaissima Lemermann E,tettes(threnberg)Ralfs L loncissima v. trooica West & West E.tetrasv.tetraction(Corda)Ralfs Clesterium ,inturvum Brebisson Pediastrum n Meyen Closteritrm spp. Nitzsch Pla4toichoeria celatinosa G. M. Smith Coelastrum Cambricum Archer Quadriau)_1 latustris (Chodat) G. M. Smith L lohsericum fiaegeli Stenedesmus abu n dans (Kirchner) Chodat Coelestrug a haegeli 1. atsndaq v. asymetrica (5hroeder) G. M. Smith Cosmarium anaulosum v. gpnj; inn,e (Rab.) West & West 1. atvndans v. breYiCauda 6. M, Smith [. oschearoscorum v. stricosum Norstedt 1. acumlMjy1 (lagerheim) Chodat G.contractumKirchner 1. armatus v. bitaudatus (Gugliell-Printr) Chodat G. colvoonuT (haegeli) Archer 1. M h at (Turpin) Lagerheim
$ ling,g Archer 1. hilvoa v. Alterarg (Reinsch) Hansgirg
[. liretum Lundell 1, denticulatus LagerheIm [. spp. Corda 1. dimorchu (Turpin) Kvetting Cructornig crucifeet (Wolle) Collins 1. intrassulatus G.jfreQuisteW1' e 1.cuadricauda(Turpin)Brebisson (.13traredia(F rchner) West & Vest iglenastrum minytym (heagelt) Collins Dittv3scheariuw ehrenberaiseum heagelt }. westil G. M Smith Q.oulchellaWood Schearoevstis gh,2,gt(Ej, Chodat riakatotheir celatinosa Ville Schearotosma granulate Roy & Bliss [uestrum spp. (hrenberg Staurastrum gmgritanum (West & West) G. M. Smith fudorina elews threnberg 1. apiculatum Brebtsson [fja.ggig droeschert (Lemerman) G. M. Smith }, brevisoinum Brebisson [. SyA111 (France) lenserman 1. curvatuT v. elenostum G. M. Smith Glococystis cla4 tonica (West & West) Lemerman }. cusoidatum Brebisson Q.gigig(Kuetting)Lagerheim 1. dejectum Brebisson
- 5. spp, heageli 1. ditbett y, rh ebotdeum West and West Golenkilta caucisoina West & West 1. manfeldtil v. flumirense Schumacher Q. radiata (Chodat) Wille 1.meascanthumLundell Qpfj,,3 sociale (Dujar.) Varm. }. earadosum v. cin%!um West & West Kirchneriella fontorta_ (Schnidle) Buhlin }. caradovum v. parvum W. West
- 5. lunaris (Kirchner) Moab. }. juberuciatum Cooke & Wille
[. oteta (W. Vest) Schnidle 1.tetracerumRalfs l L subsolitaria G 5, West 1. turoescens Denot
- 5. spp. schmidle tetraedeon arthrodesmiforme v. Sontorte votose.
Lacecheimia ciliata (Lagerheim) Chodat L g3,adjl g (Corda) Hansgirg L. lonaiseta (Lemerman) Prints 1. gaudstum v. lonaisoinum Lemerman (, cuadriseta (Lem.) G. M. Smith I. minimum (A.Braun)Hansgirg L. tut' sala Lemerman 1. Instj.g.g ( A. Braun) Hansgirg Mesostioma viride Lauterborn 1. re M are v. j n g feiling (Continued) 59
Table 2. (Continued) Tetraedron spp. Kustling Othetconas spp. Vyssotrkt letrastrum beterocanthum (hordst.) Chodet Rhizochrysis spp. Pascher Truetaria seticers (Archer) G. M. Smith 5teleitnenas g11hgips tachey Veste11a 11reatin G. M. $mith $yauta spinosa Korshikov BACILLARIOPHTCE AE 1.utellathrenberg 3 & g g gg g,ieroterhala (Kwetting) Grunca L spp threrterg L spp. Bory L'roatenetsis ameriesas (talk) Lemerman Anomoeoneis vitres (Grunow) Ross KAPIDPHYC[A[
- L spp Pfits. [hrviochreculina Lgfr.tg Lackey Asterionella formesa Hassall 1Ah1HOPHYCIAE Atthera fathattill J. Brun Dichettrococcus spp. Korshikpv Coccoaets eleccatula threnberg CRYP10PHYCIAE Cvelotella norta Crvetomonas gf.p n threnberg L menechiniana Kvetting C. 22.111 [htenberg L eseudostellicera Hustedt (. ttflera Skuja C. stelliaef.i (Cleve) Van Huerck Phndomonat tenuta $kula Cymtella EjfM11 Hilse ex. Rabenhorst Mn0PHYCIAE L igt,qi,gg Gregory A:rmeaellum ouadrid;elicatum Brebisson Cymtella spp. Agardh Aaebeena yistonstnem e Prescott
- Diclonein spp. [hrenberg 6. spp. Bory Fracilaria cretoneasts Kitten Coroccoccus limnetteus te merman Frustulia rhomboides ([hrenberg) Detoni C miner Kuetting Helesita Amt1221 (Grunow) 0. Haller C.spp,heageli 3.p,1311n,g([hrenberg)Kuttiing toeleschaerium kuetrincianum heegelt
- 3. oranulata ([hrenberg) Ralfs Gomohoscheeria lacustris Chedat
- d. oranulalg v. ancustissi$g Mueller
- un_qhg limnetica Lewermann
- 5. Italita ([hrenberg) Kuetting Lynobva spp. Agardh
! spp. Agardh Nieroevstis aerusinest Kuetzing Nitzschia acteulatts (Kuetztng) W, Smith pset11ateria ueminata Meneghtnl L gang t Hustedt Q.11mnet t es temerman g, helsatica Hustedt Q, spp. Vaucher
- 3. Eglgt (Kuetting) W, $mith PhomiUM spp. F.uetting
- 3. sublinearis Hustedt Pechidicesis cur vata Fritsch & Rich
- 3. spp. Hassall
- Synechococcus lineste ($ch, et lauterb.) Komarck Rhirosoienia spp. Ihrenberg (UGLth0PHYCEAE 9 eletnaema rotemos (Weber) Hasle
- fuelena irgg threnberg Stephanodistgg spp. (hrenberg L spp. [hrenberg Syr>edra ngg Kuetring Leceeinelos spp. Petty 1.ria4tonicathrenberg Trachelomonas acanthostoma (Stokes) Deflandre
}.rumpensKuetting 1. oulcherrima Playf air
}. gm,Tff.g v. fracilarioides Grunow 1. velvoeir a (hrenberg 1.rumrensv.scotteaGrunow L spp. [hrenberg
- 1. g Lg (httrsch) [hrenberg Olh0PHYCCA[
- 1. spp. [hrenberg Ceratium birundinella (Mueller) Schrank Tabellaria fenestrato (Lyngby) Kuetting Glenodinium D$r21.1 (Lemerman) Schiller
- 1. flocculosa (Roth) Kuetting O talustre $ chilling CHRTSOPHYCEAE Q cuadridens (Stein) Schiller Chromulina spp. Cienkowski G enodinium spp. Stein Chrysoschaere11a solitar_1,g Preitig and Takahashi Peridinium aciculiferum Lerimerman Dinobryon bavaricum Imhof g. ineensoieuum Lecrerman L cvitadeleum Imhof g, Cusillum (Pennard) Lewerman Q.sertularia[hrenberg g,wisconstneaseEddy Q.spp.[hrenberg
- Unidentified dinflagellates Erk enia igratouiciliata Skuja CHLOROH0hADOPHYCEAE rechyrton rubi-klaustri Conrad Gonvestomum derressum (Lauterborne) Lemerman Mal 1omonas eseudocoronata Prescott Q. 1stum loanoff L toasurate feiling Q.spp.Deising
$. spp. Party Unidentified flagellates 60
Table 3. Total densities (units /ml) and percent composition of major taxa (>5%) l of phytoplankton collected at locations in t.ake Norman, NC during February, May, August and November of 1990. I Locatione 20 50 95 11 0 15 9 Taron un W ml % unw ml % unwml % unw ml % un w ml % FLDHUAhr Ank. f alcatus v. mir. 77 55 Ank. epiratie 94 5.7 142 76 77 55 Coccoid greens 151 92 150 80 167 12 0 Melosita ambigua 93 55- 122 88 909 28 4 452 18 8 Mel. dietane v. nip. 134 82 Meloeira opp. 187 11 4 171 9.1 78 66 545 16 0 159 66 Rhl osolenia erlensia 90 64 Stephanodieeus opp. 208 6.1 Synura uvella 130 54. Chrysochrom. parva 94 5.7 183 98 120 9.1 Cryptomonac erose 98 60 281 11.7 Rhodomonas minuta 358 21 9 456 24 3 273 19 6 700 20 5 765 31 8 MAY Ank. falcatus v. mir. 228 10 2 220 8.1 183 65 Mictadinium pusillum 126 5.4 167 7.5 330 12 1 171 6.1 Attheya tachartaal 138 60 151 68 165 5.7 Ftngliaria crotonensis 167 58 Melostra ambig,,a 122 5.5 Meloeira distans 220 95 122 55 138 5.1 183 65 Synedre opp 139 60 228 8.1 501 17.4 Unid. chrysophytes 122 55 269 9.9 22 0 7.8 281 98 Chrysochrom. parva 142 6.1 146 66 253 93 Cryptomonas cross Rhodomonae minute 395 17.0 350 15 7 399 14 6 729 25.9 765 26 6 AUGUST Cosmar'um esphaerosporum v, stri 118 60 81 69 Coccoid greens 209 13 7 179 15 3 281 16 8 212 11 =0 427 10.7 Rhlzosoienla orienals 110 57 Synedra spp. 118 6.0 90 76 98 59 126 66 212 5.3 Unid chrysophytes 195 11.7 260 65 Cryptomonos oross 102 52 90 54 110 57 202 51 Crypt. phaseolue 98 50 Rhodomonas minuta 154 7.9 90 54 175 91 Anabaena app. 90 5.4 64 16 Anacystis incerta 85 51 118 6.1 201 5.I Raphidiopsis curvata 686 17.3 NOVEMBER Ank. Ialcatus v. mir. 110 86 171 11.9 126 58 Coccoid greens 126 51 Scan. quadricauda 81 64 155 7.2 126 5.1 Coccold groene 73 5.7 08 68 126 7.7 175 7.1 Molosira ambigua -211 12 8 123 5.7 73 30 Erkenia spp. 134 94 Cryptomonae erosa 73 5.7 102 7.1 90 54 159 7.3 224 9.1 Rhodomonaa minuta 175 13 7 183 12.8 269 16 3 3C2 16 8 419 17.1 Gomph lacustria 65 51 i 61 I - - . . - - _ _ . _ - . . . . - . . . - - _ .. - . . . - . . _. --.
Table 4 Biovolumes (mm8/m8) and percent composition of major taxa (>5%) of phytoplankton collected at locations in Lake Norman, NC during february, May, August and November 1990. Locations 2.0 50 95 11 0 15.9 Taron mm/m3 % mm/m3 % min /m3 % mm/m3 % mm'm3 % FLDRUARY Melosita ambigue 136 21 2 99 17.8 1B5 27 4 1468 65 4 685 46.1 Met distans v. alp. 44 68 Melosita opp. 76 11.9 69 12 5 222 9.9 Rhltosolenia oriensis 35 5.2 Synedre opp. 36 66 Mallomonsa caudeta 87 13.5 69 4.7 Synura vvolla 43 6.7 43 7.8 87 39 138 9.3 Chrysochrom, perve 17 7.6 Cryptomonu erosa 39 6.1 112 7.5 Rhodomonas minute 38 60 49 8$ B2 5.5 Anabaenaopp. 36 56 45 67 Peridinium inconspicuum 41 64 69 12.5 99 14.7 Peridinium pusilium 87 12.9 156 10.5 MAY Attheya 2ocharlasi 264 26 8 286 30 3 295 21 8 179 15 5 Fragitaria crotononais 125 15 2 Meiosita ambigua 92 97 98 7.3 129 11.2 Melosita distans % 60 Synedra spp. 73 7.4 52 54 69 5.1 120 10 5 pus 32.2 Mall. pseudocoronata 72 7.4 57 60 Cryptomonas erose 44 53 Rhodomonas minute 78 68 E2 10 0 Anabaena app. 90 6.7 Glenodinium gymnodinium 49 50 145 10.7 1a6 12.7 Per. pusillum
- 69 5.1 AUGUST Stsur. paradoxum 120 83 100 13 3 Stauf. manfeldtli v. fluminense 120 8.4 67 89 Attheya rachariasi 70 7.0 synedra opp. 47 6.3 52 3.3 67 66 112 87 Tabellaria fenestiata $3 5.3 Cryptomonas erosa 60 6.2 Anabaena app. 207 14 4 54 7.2 198 12.9 142 11.0 Glenodinium quadridens 145 10.0 Per, wisconsinense 133 9.2 134 13.3 Peridinium app. 210 14.6 210 28.1 790 51.3 317 31.5 453 35.1 NOVEMBER Atthoya rachariaal 70 16 4 70 16 6 54 6.1 Melooira ambigua 55 13.1 68 16.2 320 35 6 186 24 0 111 16 6 Rhlrosolenia oriensis 27 6.4 Synodra spp. 22 5.1 49 6.4 Tabellaria fenestrata 40 94 44 10.5 Cryptomonas eross 29 69 40 96 63 8.1 B9 13 3
! Crypt reflexa 34 5.1 l Rhodomonas minuta 39 50 45 6.7 Anabaena spp. 27 6.3 Ceratium hirundinella 196 21.9 65 84 Peridinium spp. 53 68 Phacus tortus 24 55
VI. ZOOPLANKTON INTRODUC110N The objectives of the Lake Norman Maintenance Monitoring Program for zooplankton are to:
- 1. Dese. ribe quarterly patterns of zooplankton standing crops at selected locations on Lake Norman, and
- 2. Compare zooplar.kton data collected during this study (February, Hay, August, and November 1990) with historical data collected during these months.
Previous studies on Lake Norman zooplankton populations have demonstrated a bimodal seasonal distribution with peaks occurring in spring and fall. Considerable spatial and year to year variability has also been observed (Duke Power Company 1976, 1985; Hamme 1982; Menhinick and Jensen 1974). METH0DS AND MATERIALS Quarterly zooplankton samples were collected at locations 2.0, 5.0, 9.5, 11.0, and 15.9 (Chapter 111, figure 1). Duplicate 10 m to surface and bottom to surface net tows were taken at these locations on 28 february, 24 May, 31 August, and 2 November 1990. Field and laboratory nethods for zooplankton standing crop analysis were reported in Hamme (1982). Zooplankton standing crop data from 1990 were compared primarily with corresponding data from quarterly monitoring in 1989. RESULTS AND DISCUSSION Elandin9 01.9D Zooplankton densities in 1990 were generally higher in 10 m to surface samples than among bottom to surface samples except in february when little difference was observed (Table 1; figure 1). This vertical population stratification was also observed in previous years (DPC 1988, 1989 and 1990) and is probably 63
related to the ability of zooplankton to maintain their position in the water column in response to the light gradient (Hamme 1982). Zooplankton standing crops in 1990 were generally highest in February and lowest in August. The large population observed uplake in Februay was in contrast to 1989 where : highest densities were found in May (Figure 2). However, since the February samples in 1990 were collected at the end of the month, this could be considered an early spring sample which is generally the time of maximum zooplankton standing crops (Hamme 1982). As in 1989, zooplankton standing crops in the surface tows were, in general, greater uplake than downlake (Figure 1). Zooplankton densities during February, May, August, and November of 1990 were generally within the range of those observed during these months of 1989 and previous years (DPC 1988, 1989, and 1990). Zooplankton densities in the mixing zone (Locations 2.0 and 5.0) in 1990 especially were quite similar to those observed in 1989 (Figure 2). Densities further uplake appeared to be higher in February ano May compared with 1989 (Figure 2), especially at Location 11.0 (10 m to surface) in February, which were over three times higher than those observed in 1989 (188,400 no./mi and 54.6 no./ms, respectively). This high density, however, is similar to zooplankton standing crops observed at Location 15.9 in February of 1989. In fact, overall the range of zooplankton densities observed at all locations in 1990 (high of 188,400 no./m' at Location 11.0 in February and low of 15,600 no./m> at Location 2.0 in August) is very similar to that observed in 1989 (high of 189,600 no./mi at Location 15.9 in February and low of 17,500 no./mi at Location 11.0 in August). Community Composition Fifty-three zooplankton taxa have been identified in sampies collected since the Lake Norman Maintenance Monitoring Program was initiated in August 1987 (Table 2). No new zooplankton taxa were identified in samples collected in 1990. Rotifers generally dominated zooplankton assemblages at all locations during 1990, followed closely in importance by copepods, with cladocerans a distant 64
l l third (Table 1; figure 3). Rotifers dominated zooplankton populations of most I samples collected in february and August, whereas copepods dominated most samples collected in May and November. Cladocerans never comprised more than 25% of the total zooplankton density at any location in any month, and were never dominant in 1990. The highest percent composition of rotifers was recorded at Location 15.9 in August, where rotifers accounted for more than 80% of the total densities in both 10 m to surface tows and bottom to surface tows (figure 2). Hamme (1982) also found that highest rotifer densities generally occurred at uplake locations. During February 1990, Keratella and _Polvarthra were codominant in rotifer populations at all locations with Collotheca also occassionally becoming important. Asolanchna was the dominant rotifer taxon at all locations except 11.0 in May where Synchaeta was more abundant. Keratella and Collotheca were again important rotifers at all locations in May as in february. Conochilus was the dominant rotifer at most locations in August in 1990 as in 1989. It was especially abundant at Location 15.9 where it comprised about 70% of the total zooplankton densities in both 10 m to surface and bottom to surface tows. Asolanchna, P_o.1varthra, Keratella, and Hexarthra were also important rotifer taxa in August. In November 1990, Keratella and Polvarthra again were codominant rotifers at most locations with Conochilus important at some downlake locations. These taxa were also the most abundant rotifers observed during 1989 and in previous years (DPC 1988, 1989 and 1990)(Hamme 1982). As in 1989, copepoa populations were dominated by immature forms (primarily nauplii and cyclopoid copepodids with some calanoid copepodids) during all sampling periods of 1990. With the exception of J.tapocyclool spp. in the bottom to surface tow at location 5.0 in August, no adult copepod comprised more than 5% of the total zooplankton densities at any time. No distinct spatial trend in copepod abundance was detected for samples collected in 1990. Copepods appeared to be slightly more abundant overall in 1990 compared with 1989 (Figure 2)(DPC 1990). Bosmina was the most abundant cladoceran observed in samples collected in 1990, just as it had also been in 1969 (DPC 1990) and in previous years (Hamme 1982), ILQJaing was es'pecially abundant in February, when it comprised more 65
than 5% of the total density at all locations, including the high for the year of 21.3% (40,128 no./m2) at Location 11.0. futsminoosis was an important i constituent of cladoceran populations at Location 2.0 in August. Daphnia spp. comprised over 5% of the total density at Location 15.9 in November in both 10 l m to surface and bottom to surface samples. Cladoceran densities appeared to be slightly lower in 1990 than 1989 especially in August (figure 2). No distinct spatial trend in cladoceran abundance was observed in 1990.
SUMMARY
Zooplankton densities, in general, were slightly higher in 10 m to surface samples than in bottom to surface samples in 1990 as in 1989. Total zooplankton standing crops were generally highest in february and, except for Location 15.9, lowest in August. Since the february sampling was done at the end of the month, this could be considered early spring in Lake Norman. Therefore, this seasonal trend was not unlike past studies where zooplankton peaks were often observed in the spring. The overall range of zooplankton densities observed during 1990 was similar to the range observed in 1989. Rotifers dominated zooplankton standing crops throughout 1990, as they did in 1989, followed closely in importance by copepods. Rotifers were generally dominant at most locations in February and August, and copepods m re dominant at most locations in November. Cladocerans were f.ever dominant in 1990. Major rotifer taxa observed in H30 were Keratella, Polvarthra, and Conochilus. Copepod peri.ations were dominated by immature forms (nauplii and cyclopoid copepodids). As in 1989, Bosmina was the most abundant cladoceran taxa obserred at all locations, with himinopsis abundant at Location 2.0 in Aupst and Qaphnia spp, at Location 15.9 ..i November. All of the major genera identified during 1990 were also listed as among the most abundant taxa in 1989 and during previous years. Copepod percent composition by month in 1990 was slighty higher than in 1989, while rotifers and cladocerans were lower. l l 66
LITERA1URE CllED Duke Power Company. 1976. McGuire Nuclear Station, Units 1 and 2, Environmental Report, Operating License Stage. 6th rev. Volume 2. Duke Power Company, Charlotte , NC. Duke Power Company. 1985. McGu' ire Nuclear Station, 316(a) Demonstration. Duke Power Company, Charlotte, NC. Duke Power Company. 1988. Lake Norman Maintenance monitoring program: 1987 Sunrary. Duke Power Company. 1989. Lake Norman Maintenance monitoring program: 1988 Summary. Duke Power Company. 1990. Lake Norman Maintenance monitoring program: 1989 Summary. Hamme, R. E. 1982. Zooplankton, la J. E. Hogan and W. D. Adair (eds.). Lake Norman summary Technical Report DUKEPWR/82-02 p. 323-353, Duke Power Company, Charlotte, NC. 460 p. Menhinick, E. F. and L. D. Jensen.1974. Plankton populations. ID L. D. Jensen (ed.). Environmental responses to thermal discharges from Marshall Steam Station, Lake Norman, North Carolina. Electric Power Research Institute, Cooling Water Discharge Research Project (RP-49) Report No. 11., p. 120-138, Johns Hopkins University, Baltimore, MD 235 p. 67
Table 1. Total zooplankton densities (no./m2), densities of major zooplankton taxonomic groups, and percent composition (in parenthesis) of major taxa in 10 m to surface (10-S) and bottom to surface (B-S) net tow samples collected from Lake Norman in 1990. Sample location 1 big lypt Taxon 2 . 0._. 5.0 9.5 11.0____15.9 02/28/90 10-S COPEPODA 18.1 5.8 39.6 47.0 31.2 (28.7) (18.5) (51.8) (25.0) (16.0) CLAD 0CERA 11.3 3.1 8.5 45.5 6.3 (17.8) (9.8) (11.2) (24.1) (6.7) ROTIFERA 33.8 22.3 28.4 95.9 56.2 (53.4) (71.7) 11L.11 (50.9) (60,1) TOTAL 63.2 31.1 76.4 188.4 93.5 B-S COPEP00A 16.2 5.9 35.4 29.4 16.5 (depth [m] (23.6) (19.0) (27.8) (17.2) (37.6) of tow for each CLAD 0CERA 10.4 6.3 9.3 30.8 4.3 location: (15.1) (20.2) (14.2) (18.1) (9.7) 2.0 32 5.0 20 ROTIFERA 42.0 18.9 20.5 110.3 23.2 9.5-18 111111 (60.9) (31.4) (64.7) (52.7) 11.0 27 TOTAL 68.6 31.0 65.1 170.5 43.9 15.9 21) 05/24/90 10-S COPEP0DA 35.4 33.8 25.5 36.5 NS (62.9) (44.8) (37.8) (48.2) CLAD 0CERA 3.9 3.8 1.8 3.9 NS (6.9) (5.0) (2.7) (5.1) ROTIFERA 17.0 37.8 40.1 35.4 NS 11LZ1 (50.1) 111dl LEll TOTAL 56.3 75.4 67.4 75.7 NS B-S COPEPODA 22.0 31.3 24.5 26.6 NS (depth [m] (70.0) (59.3) (51.9) (57.4) of tow for each CLADOCERA 3.2 3.0 1.9 3.9 NS location: (10.1) (5.7) (4.1) (8.4) 2.0 31 5.0 20 ROTIFERA 6.3 18.5 20.7 15.8 NS 9.5-21 (19.9) 111191 (44.0) (34.2) 11.0-26 TOTAL 31.4 52.8 47.2 (6.3 NS 15.9 21) 68 (Continued)
Table 1 (continued) Sample locations QA11 Jype_ Taxon ,_ 2. d _ 5.0 9.5 11.0 15.9 08/31/90 10-S COPEPODA 6.9 8.0 7.6 8.3 9.7 (25.3) (17.4) (23.4) (19.4) (9.1) CLA00CERA 4.5 2.9 2.1 4.9 1.9 (16.5) (8.7) (8.3) (11.4) (1.8) ROTIFERA 15.8 22.8 15.4 29.6 94.6 (58.2) (67.6) (61.4) (69.3) (89.0) TOTAL 27.1 33.7 25.1 42.8 106.3 B-S COPEPODA 7.2 11.7 6.9 7.9 10.8 (depth [m] (46.3) (41.3) (35.6) (39.5) (13.2) of tow for each CLAD 0CERA 1.5 4.0 1.9 2.5 4.4 location: (9.4) (14.3) (10.0) (12.8) (5.4) 2.0 31 5.0 20 ROTIFERA 6.9 12.6 10.6 9.5 66.3 9.5-21 (44.3) (44,4) (54.4) (47.7) (81.4) 11.0 26 15.9 21) TOTAL 15.6 28.4 19.4 19.9 81.5 11/02/90 10-S COPEP00A 19.5 15.7 23.8 17.3 33.0 (44.8) (54.3) (52.0) (51.1) (42.7) CLAD 0CERA 7.7 3.1 5.2 2.2 6.7 (17.7) (10.7) (11.3) (6.4) (8.7) ROTIFERA 16.3 10.1 16.8 14.4 37.6 11Ljil (35.0) M (42.4) (48.6) TOTAL 43.6 28.9 45.8 33.9 77.3 B-S COPEP00A 14.4 15.2 20.4 13.7 24.4 (depth [m] (55.9) (54.8) (49.9) (46.8) (58.3) of tow for each CLAD 0CERA 5.0 2.7 5.9 1.4 4.4 location: (19.6) (9.6) (14.4) (4.7) (10,5) 2.0 28 5.0-19 R0llFERA 6.3 9.9 14.6 14.2 13.0 9.5 18 111,11 (35.6) (35.7) (48.5). (31.2) 11.0-24 TOTAL 25.7 27.8 40.8 29.2 41.8 15.9 21) 69
I Table 2. Zooplankton taxa identified from samples collected in Lake Norman on August and November 1987 and February, May, August, and November 1988, 1989, and 1990. COPEPODA Conochilgi unicornii (Rousselet) Cyclops thomasi (S. A. Forbes) C spp. Hlava L. spp. (O. F. Muller) Gastrocus spp. Imhof Diaotomus bergei Marsh Hexarthra spp. Schmarda Q. mississioniensis Marsh Kellicotia hostonensis (Rousselet) Q. Dallidus Herick K. spp. Ahlstrom Q. spp. Marsh Keratella spp. Bory de St. Vincent tiesocyclops flits (S. A. Forbes) Lecane spp. Nitzsch M. spp. Sars Macrocheatus spp. Perty Trococyclops crasinus (Fischer) Honostyla 1_tenroo31 (Meissener)
- 1. spp. Kiefer M. spp. Ehrenberg Calanoid copepodites Ploeosoma truncatunj (Levander)
Cyclopoid copepodites E. spp. Herrick Nauplii Polvarthra eurvotera (Weirzeijski) E. vulaaris Carlin CLAD 0CERA E. spp. Ehrenberg Ptvaura spp. Ehrenberg Bosmina lonairostris (O. F. Muller) Synchaeta spp. Ehrenberg H. spp. Baird Trichocera a pucina (Weireijski) Bosminoosis deitersi Richard 1. cylindrica (Imhof) Ceriodachnia spp. Dana I. spp. Lamarck Q1phnia ambiaua Scourfield Unidentified Bdelloidea D. Darvula Fordyce D. spp. Muller INSECTA Diachanosoma spp. Fischer Holooedium amazonicum Stingelin Chaoborgi spp. Lichtenstein B. spp. Zaddach LepigdgrA kindtii (Focke) Ilvocrvotui sordidus (Lieven) Sida crystallina 0. F. Muller ROTIFERA Anuraeopsis spp. Lauterborn Asolanchna spp Gosse Brachionus caudata Barrois and Daday B. havanaensis Rousselet H. aatulus 0. F. Muller Chromoaaster spp. Lauterborn Collotheca spp. Harring [tnochiloides spp. Hlava 70 a
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unne x icoo/m3 1989 1990 im Mixing " Zone a -- (2.0 & 5.0) 4o _.
~
0 fob "" ' " May Aug PJov Feb May Aug f4ov units x 1000/m3 no .. Loc. , :.. 9.5 - 40 -- 0 Feb May Aug Nov Feb May Aug Nov units x 1000/m3 200 15o -- Loc i. . 11.0 g q o Feb May Aug Nov feb May Aug Nov M Rotifers O Copepods O Cladocerans Figure 2. Comparison of zooplankton density and composition in 10 m to surf ace net tows collected in Lake Norman, NC in 1989 and 1990. 72
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VII. FISHERIES INTRODUCT10N in accordance with the NPDES permit for McGuire Nuclear Station (MNS), monitoring of specific fish population parameters was continued during 1990. The objectives of the fish monitoring program for Lake Nornan during 1990 were to:
- 1. determine taxonomic composition, standing stock, and density of fish at the McGuire Nuclear Station discharge from cove rotenone samples;
- 2. determine density and distribution of fish with hydroacoustic!
in the MNS mixing zone when surface water temperatures reached 32, 35, 37, and then returned to 32 C;
- 3. note any occurrence of fish mortalities nu? +be MNS mixing zone during the summer period; and
- 4. conduct angler diary surveys of selected striped bass anglers to gather information about st'iped bass distribution through the summer period.
The primary focus of this report will be to compare data collected in 1990 with data collected during MNS operation with a 35 C discharge limit (1984 through 1983). MATERIALS AND METHODS Taxonomic composition, standing stock (kg ha-1), and density (number ha-l) of fish were determined with cove rotenone samples during May and August 1990 at MNS discharge Location 4.0, using methods described in 1989 (Duke Power Company 1990) and (Siler et al. 1982) (Chapter 3, figure 1). A 600 ft x 40 ft deep x 1/4 inch mesh purse seine was set in the main channel and near the MNS discharge after sunset in June, August, and 74
I October 1990 to collect limnetic fish. The fish captured with the purse seine were identified to species, counted, and a subsample of 500 were measured (mm, TL). Density of fish in the limnetic areas of the MNS mixing zone was determined with 120-KHz hydroacoustic gear on 18 June, 16 July, 8 August, and 1 October 1990 after sunset. We sampled in the MNS mixing zone using methods similar to 1988 and 1989 (Duke Power Company 1990). Hydroacoustic samples were collected along transects in the mixing zone for MNS (Figure 1). The main channel of Lake Norman was searched for dead and moribund fish in conjunction with physicochemical samples during June, July, August, and September. Additional searches for stressed and dead fish were also conducted twice per week in the MNS mixing zone in late June, July, and early August 1990. The striped bass angler diary program, initiated in 1989 to provide seasonal distribution of striped bass in Lake Norman, catch rates and harvest, and size distribution of angler caught striped bass was continued in 1990. RESULTS AND DISCUSSION The fish community, as determined by cove rotenone sampling, at Location 4.0, was similar to 1984 through 1989 cove rotenone species compostions (Duke Power Co., 1990). In 1990, 23 fish species were collected at location 4.0 (Table 1). Standing stock in May 1990 was similar to August cnllections from previous years, however, August standing stock declined dramatically to 14.34 kg/ha (Figure 2). This is the lowest we have ever recorded for a Lake Norman cove. Hydroacoustic density estimates reflected the movement of limnetic fish species away from the MNS discharge when water temperatures exceeded 31 C. Censities were lower near the MNS discharge (transect 4) than at any other area sampled in 1990 (Table 2). Density estimates were highest in the back of Ramsey Creek, and in the main channel on 18 June (Figure 3). By 16 July densities were greatest in the main channel i 7S
(Figure 4). Densities at the main channel locations remained highest on 8 August (Figure 5), but by 1 October fish moved closer to the MNS discharge (Figure 6). Depth distribution of fish was also related to water temperature. During the 18 June sample, the highest fish densities were near the surface where water temperatures were 29 C at transect 9 and 31 C (coolest available water) at transect 4 (MNS discharge)(Figure 7). By the 16 July sample, the highest densities were at 8 meters (26o C) at traasect 9 and 10 meters (31 C) at transect 4 (Figure 8). The fish moved deeper as the water temperature increased in August (Figure 9). Limnetic fish returned to the surface by the 1 October sample where water temperatures were 26 C and 29o C at transects 9 and 4, respectively (Figure 10). Purse seine samples conducted at the time of hydroacoustic data collection in June, August, and October revealed that over 99.6% of the fish in the limnetic region of Lake Norman were threadfin shad (Table 3). The length frequency distribution of purse seined threadfin shad were similar to lengths calculated from hydroacoustic target strengths with Love's dorsal aspect equation (Love, 1971; Figure 11). The mean length of threadfin shad captured in June and October purse seining was greatt:r than hydroacoustics, however, in August they matched well. Hydroacoustics was set to effectively sample all fish greater than 35 mm, but subsampled to 17 mm. The 1/4-inch mesh purse seine effectively samples threadfin shad greater than 50 mm, but we captured threadfin shad 27 mm long. This bias in size selectivity for larger shad by the purse seine was for all samples, but was more evident in June and October. Eight striped bass were reported caught in the voluntary striped bass angler diary program during the summer (June-August) period, declining from 21 in 1989 (Table 4). No fish were caught in the MNS mixing zone in either year during summer. The striped bass caught in summer 1990 were in the Mountain Creek (Zone 3) and riverine (Zone 6) areas. However, the small number of anglers reporting informatiun does not provide good distribution information about striped bass during the 76
summer period. FUTURE STUDIES
- Fish distribution and density in the MNS mixing zone in 1991 using hydroacoustics and purse seine when water temperatures approximate 32, 35, 37, and 32 C to continue to evaluate the change in the discharge temperature limit from 35 to 37.2 C.
- Plan a lakewide creel survey for December 1991 through November 1992 in cooperation with NCWRC to collect striped bass distribution information required for the NPDES permit.
- Continue striped bass mortality monitoririg throughout the summer.
SUMMARY
-The MNS warmwater discharge does affect the behavior of fish in lower Lake Norman. Rotenone standing stock declined from pre-1984 levels of approximately 140 kg/ha to 74 kg/ha after 1984, and 14 kg/ha in August 1991. This change in the standing stock near the MNS discharge indicates that the fish are avoiding the warmer water in the summer.
May 1990 rotenone standing stock was similar to previous MNS operational years, however, lit + oral fish populations probably selected cooler water away from the MNS discharge in August, thereby, reducing the standing stock in the cove further in August. The hydroacoustic data better shows the movement of fish away from the heated water, when temperatures { exceed 31 C. Fish moved to areas in lower Lake Norman where ,. temperatures were below 31 C by moving away from the discharge area, I and moving deeper when summer heating of the surface water pushed l: surface water temperatures above the 26 - 28 C preferred by threadfin L shad and other warmwater fish species (Welch and Wojtalik, 1968). The voluntary angler creel is not providing sufficient information to determine distribution of striped bass in Lake Norman as required by the NPDES permit. A creel survey will need to be implemented in 1991 - 1992 to provide information about the distribution of striped bass throughout the year. 'This creel survey will be a cooperative study with NCWRC, 77
will provide' information about all species of game fish, will allow comparison of harvest and fishing pressure during MNS operation to pre-MNS operation in 1982, and will provide distribution of striped bass using a larger angler population than is presently available with the voluntary creel. 78
l LITERATURE CITED Duke Power Company. 1990. Lake Norman: 1989 maintainance monitoring program, McGuire Nuclear Station. Love, R. H. 1971. Dorsal-aspect target strength on an individual fish. Journal of the Acoustical Scciety of America 49:816-823. Siler, J.R.; Lewis, R.E.; Baker, B.K.; Vaughan, G.E.; Hansen, R.A. 1982. Chapter 10. Fish, in Hogan, J.E. and W.D. Adair (eds.). Lake Norman Summary. Duke Power Technical Report No. DUKE PWR/82-02. Duke Power Company, Charlotte, NC. 460 p. plus appendices. Welch, E.B. and T.A. Wojtalik. 1986. Some effects of increased water temperature on aquatic life. TVA, Division of Health and Safety, Water Quality Branch, Chattanooga, TN. 48pp. t 79
_ _ . . . _ - - . ~. - . - - - . . _ . _ . - Table 1.. Standing stock'(kg/ha) and density (no/ha) for cove 4.0 in May and August 1990. May August Taxa kg/ha no/ha kg/ha no/ha Dorosoma cepedianum 4.88 20 0.92 3 Dorosoma petenense 4.19 562 0.42 430 Cyprinus carpio 14.21 lo 0.84 1 Notemigonus crysoleucas 0.02 1 0.00 0 Notropis chloristius 0 01 2 0.00- 0 Notropis hudsonius 0.uo 1 0.00 0 Notropis niveus 0.37 113 0.27 221 Pimephales promelas 0.00 1 0.00 0 Carpiodes cyprinus 18.46 25 0.00 0 Ictalurus catus 2.05 lo 0.01 4 Ictalurus punctatus 0.00 0 0.17 6 Plyodictis olivaris 8.73 1 0.12 1 Gambusia affinis 0.00 2 0.00 0 Norone chrysops 0.09 1 0.00 0 Lepomis auritus 3.12 306 2.54 260 Lepomis gibbosus 0,01 1 '0.00 0 Lepomis gulosus 0.43 51 0.23 43 Lepomis macrochirus 4.09 610 1.80 1043 Lepomis microlophus 1.48 51 0.14- 2 Lepomis hybrid 0.52 35 0.65 16 Micropterus salmoides 5.90 1902 0.23 23 Pomoxis nigromaculatus 2.16 13 0.00 0 l Etheostoma olmstedi 0.00 1 0.00 0 l Perca flavescens 0.94 101 0.00 0 TOTAL 71.66 3820 14.34 2053 l L 80
Table 2. Hydroacoustic density estimates (no/ha) by transect. TRANSECT 18-Jun-90 16-Jul-90 8-Aug-90 1-Oct-90 7,217 5,668 3,824 1,843 1 9,634 7,906 5,909 5,836 2 2,990 6,204 6,296 4,531 3 1,081 2,737 3,069 1,466 4 5 1,603 9,729 8,027 8,615 1,562 8,921 7,385 3,962 6 7 6,446 25,000 11,102 1,813 8 3,702 20,546 9,148 3,664 9 6,163 33,837 10,246 5,369 4,949 not sampled 8,952 2,321 10 81
_ _ . - _ - - . . _ . _ _ _ . _ _ _ _ _ . _ _ _ _ _ _ _ -._ ___ _. .~ . - . , s
- Table 3, Fish caught with 600 ft X 40 ft X 1/4 inch mesh purse seine in Lake Norman near McGuire Nuclear Station in 1990.
DATE SPECIES 6/13/90 6/14/90 6/18/90 8/23/90 10/1/90 Dorosoma cepedianun 3 1 2 0 0 Dorosoma petenense- 13,489 4,013 17,233 3,210 5,264 (ctalurus furcatus 0 0 2 0 0 Ictalurus punctatus 1 3 1 0 0 Morone chrysops 3 0 3 0 0 Horone saxatilis 0 3 0 0 0 Pomoxis nigromaculatus 2 1 4 5 19 i. 82
o . Table 4. Number of striped bass caught by anglers participating in , the voluntary creel. ZONE 1 2 3- 4 5 6 8 9 Apr-89 1- 3 7 13 25 1 0 0 May-89 -0 0 3 2 5- 0 1 0 Jun-89 0 0 8 0 4' 1 0 1-Jul-89 0 2 1 0 0 -1 0 0 Aug-89 0~ 0 0 0 0 3 0 0 Sep-89 0 0- 0 0 0- 3 0 0 Oct-89: 0 0 0 0 0 0 0 0' Nov-89 0 0 0~ 0 27 0 0 2 Dec-89' 7 0 21 29 31- 0 0 0 Jan-90 3 5 0 18 0 0 0 1-Feb-90 0 0 0 10 10 0 0- 0 Mar-90 0- 0- 3 8 8 0 0 0 Apr-90 0- 1 3 12 6 0 0 0 May-90 0 0 0 0 1 -0 0 0 Jun-90 0 0 0 0 0 0 0 0 Jul-90 0 0 3 0 0 4 0- 0-Aug-90 0 0 0 0 0 1 0 0
-Sep 0 0 0 0 0 0 -0 0-Oct-90 0 0 9- 0 3 0 -0 0 Nov-90 0 0 8 0- 34 0 0 0 Dec-90 0 0 0 0- 19 0 0 'O 83
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i l l u . Figure 7. Depth distribution of fish near the MNS discharge (transect 4) and in an l area with ambient surface water temperatures (transect 9) on 18 June 1990.
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Figure 8. Depth distribution of fish near the MNS discharge (transect 4) and in an area with ambient surface water temperatures (transect 9) on 16 July 1990. 30 ' ze ' , e
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i Figure 10. Depth distribution of fish near the MNS discharge (transect 4) and in an area with ambient surface water temperatures (transect 9) on 1 October 1990.
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- j. Length (mm) l~
l Figure 11. Length frequency distribution for purse seine and hydroacoustics near the MNS discharge. 94}}