ML20133F186

Lake Norman:1995 Summary Maint Monitoring Program McGuire Nuclear Station:Npdes NC0024392

ML20133F186
Person / Time
Site:	McGuire, Mcguire
Issue date:	12/31/1996
From:	DUKE POWER CO.
To:	NRC OFFICE OF INFORMATION RESOURCES MANAGEMENT (IRM)
References
NUDOCS 9701140097
Download: ML20133F186 (85)

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January 7, 1997 U. S. Nuclear Regulatory Commission Document Control Desk i Washington, D.C. 20555 '

Subject:

McGuire Nuclear Station Docket Nos. 50-369, 370 Pursuant to Duke's Corporate Environmental Manual, please find attached the Annual Lake Norman Environmental Summary Report for 1995 as required by NPDES permit NC0024392. This report includes detailed results and data comparable to that of previous years.

Questions concerning this report should be directed to Kay Crane, i McGuire Regulatory Compliance at (704) 875-4306.

H. B. Barron, Vice President  !

McGuire Nuclear Station cc: Mr. Victor Nerses, Project Manager .

Office of Nuclear Reactor Regulation U.S. Nuclear Regulatory Commission Washington, D.C. 20555 Mr. Luis Reyes, Regional Administrator U.S. Nuclear Regulatory Commission Region II 101 Marietta Street, Suite 2900 Atlanta, Georgia 30323 Mr. Scott Shaeffer Senior Resident Inspector McGuire Nuclear Station

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i LAKE NOltM AN: 1995 SUMMAJn' I

l l MAINTENANCE MONITOlllNG PitOGRAM I

McGUIllE NUCLEAR STATION: NPDES No. NC0024392 i

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13339 IIAGERS FERRY ltOAD IlUNTEllSVILLE, NORTII CAROLINA 28078 DECEMllEll 1996

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V TAllLE OF CONTENTS Page EXECUTIVE

SUMMARY

i LIST OF TABLES iv LIST OF FIGURES v CHAPTER 1: McGUIRE OPERATIONAL DATA 1-1 Introduction 1-1 Operational data for 1993 1-1 CHAPTER 2: WATER CHEMISTRY 2-1 Introduction 2-1 Methods and Materials 2-1 Results and Discussion 2-2 l

Future Water Chemistry Studies 2-8 Summary 2-8 Literature Cited 2-9 CHAPTER 3: PHYTOPLANKTON 3-1 Introduction 3-1 Methods and Materials 3-1 Results and Discussion 3-2 Future Phytoplankton Studies 3-7 Summary 3-7

p Literature Cited 3-8 CHAPTER 4

ZOOPLANKTON 4-1 Introduction 4-1 Methods and Materials 4-1 Results and Discussion 4-2 Future Zooplankton Studies 4-5 Summary 4-6 Literature Cited 4-6 CIIAPTER 5: FISHERIES 5-1 Introduction 5-1 4 Methods and Materials 5-1

Results and Discussion 5-1 Future Fisheries Studies 5-2 O

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EXECUTIVE SUMM ARY As required per the National Pollutant Discharge Elimination System (NPDES) permit number NC0024392 for McGuire Nuclear Station (MNS), the following annual report has been prepared. This report summarizes environmental monitoring of Lake Norman conducted during 1995.

OPERATIONAL DATA FOR 1995 Monthly capacity factors of MNS during 1995 averaged over 50% for all months for both units except in December for Unit 1. The average nionthly discharge temperature was below the permit limit for all months. During July, August, and September, when conservation of cool water and discharge temperatures are most critical, the thermal limit for MNS increases from a monthly average of 95 F to 99 F. The average monthly discharge temperature was 94.4 F (34.7 C) for July,98.7 F (37.1 C) for August, and 94.7 JF (34.8 C) for September 1995. Use of low level intake water was necessary in August 1995 for compliance with the thermal limit for MNS. Low level intake water was pumped only through the condenser of l p, Unit i from August 22 - 30,1995.

J WATER CllEMISTRY DATA Temporal and spatial trends in water temperature and DO data collected monthly in 1995 were similar to those observed historically. Temperature and DO data collected in 1995 I were within the range of previously measured values. Reservoir-wide isotherm and isopleth information for 1995, coupled with heat content and hypolimnetic oxygen data, illustrated that Lake Norman exhibited thermal and oxygen dynamics characteristic of historic conditions and similar to other Southeastern reservoirs of comparable size, depth, flow conditions, and trophic status.

All chemical parameters measured in 1995 were within the concentration ranges previously reported for the lake during both MNS preoperational and operational years.

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PIlYTOPLANKTON DATA 1

Chlorophyll a concentrations at all locations during 1995 were within historical ranges and in

, the mesotrophic range. The maximum chlorophyll a value observed in 1995 (12.4 mg/l) was j far below the NC State Water Quality Standard of 40 mg/1.

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Seston dry weights were not as variable spatially and temporally in 1995 as in 1994; the trend i ofincreasing values downlake to uplake was not as apparent in 1995 as in previous years.

< This indicates that more stable conditions existed prior to sampling times during 1995.

1 Based on proportions of ash free (organic) dry weight to dry weight, higher amounts of organic material were present in 1995 than in 1994.

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1 Total phytoplankton densities and biovolumes observed in 1995 were within the range of l

those observed in previous years. The maximum density and biovolume were below state a

standards of 10,000 units /ml and 5,000 mm3 /m 3 and no bloom conditions were recorded at times of sampling. Densities and biovolumes were lowest in February and highest in May, as

! was the case in 1994. The previous year's trend ofincreasing values downlake to uplake was i O neieeennarentin1995.iedicatinsecheeseiu8vetiaiveriabiiiir.

1 i ZOOPLANKTON DATA Total zooplankton standing crops were generally highest in May and lowest in August, and i

densities were most often higher in epilimnetic samples than whole column samples in 1995.

j Comparisons of each quarter from year to year showed that epilimnetic zooplankton densities I

from most Lake Norman locations in February and May peaked in 1995, indicating long term

. increases in zooplankton productivity during these months since 1991. In August and November of 1995, zooplankton densities were within historical ranges. .

Overall, rotifers dominated zooplankton standing crops throughout most of 1995, followed closely by copepods, as has been documented previously. Major rotifer taxa observed in 1995 were Synchaeta, Keratella, Polyarthra, and Trichocerca. Copepod populations werc ii 4

. - . - - - - = -- . . .=- . _ _ - - - . .. _ ._

O demineted by immature ferms, with adeits seidem ecceeeties for mere thee 5

• ef zooplankton densities. Bosmina was the predominant cladoceran taxon of 1995. Trends in

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community composition and taxon abundance were similar to those observed during previous l

studies.

FISHERIES DATA Availability of suitable pelagic habitat for adult striped bass in Lake Norman in 1995 was generally similar to historic conditions (Chapter 2). Reservoir-wide habitat elimination occurred for about one month in 1995. These conditions were better than observed in 1993 but somewhat more restrictive that in 1994 when habitat was never eliminated in the reservoir.

The MNS mixing zone was surveyed for striped bass mortalities during summer sampling trips on the lake, and during the last week of July through August of 1995 specifically to locate dead or dying fish. Only one dead striped bass >500mm was reported in 1995.  ;

D U Winter gill netting for striped bass condition yielded 70 fish ranging in length from 281 mm I to 622 mm. Individual fish length, weight, and age of all striped bass collected in the study were reported to the NCWRC.

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LIST OF TABLES Page Table 1-1 McGuire Nuclear Station (MNS) 1994 capacity factors 1-2 i Table 2-1 Water chemistry monitoring program schedule 2-11 Table 2-2 Water chemistry methods and detection limits 2-12  !

Table 2-3 Heat content calculations for Lake Norman in 1993 and 1994 2-13 Table 2-4 Comparison of Lake Norman with TVA reservoirs 2-14 Table 2-5 Water chemistry data for 1994 for Lake Norman 2-15 Table 3-1 Mean chlorophyll a concentrations in Lake Norman 3-10 Table 3-2 Duncan's multiple range test for Chlorophyll a 3-11 Table 3-3 Total phytoplankton densities from Lake Norman 3-12 Table 3-4 Duncan's multiple range test for phytoplankton densities 3-13 ,

Table 3-5 Duncan's multiple range test for seston in Lake Norman 3-14 Table 4-1 Total zooplankton densities and composition 4-8  !

Table 4-2 Duncan's multiple range test for zooplankton densities 4-10 Table 4-3 Zooplankton taxa identified in Lake Norman 1994 4-11 O

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V LIST OF FIGURES Page Figure 2-1 Map of sampling locations on Lake Norman 2-18 Figure 2-2 Monthly precipitation near McGuire Nuclear Station 2-19 Figure 2-3 Monthly mean temperature profiles in background zone 2-20 Figure 2-4 Monthly mean temperature profiles in mixing zone 2-22 Figure 2-5 Monthly temperature and dissolved oxygen data 2-24 Figure 2-6 Monthly mean dissolved oxygen profiles mixing zone 2-25 Figure 2-7 Monthly mean dissolved oxygen in background zone 2-27 Figure 2-8 Monthly isothenns for Lake Norman 2-29 Figure 2-9 Monthly dissolved oxygen isopleths for Lake Norman 2-32 Figure 2-10a 11 eat content of Lake Norman 2-35 Figure 2-10b Dissolved oxygen content of Lake Norman 2-35 Figure 2-11 Striped bass habitat in Lake Norman 2-36 Figure 3-1 Chlorophyll a measurements of Lake Norman 3-15 Figure 3-2 Mean chlorophyll a concentrations by year 3-16 Figure 3-3 Chlorophyll a concentrations by location 3-17 O Fiaere 2-4 cias8 comnesitien ef nhrtoniankton 3-i9 Figure 4-1 Zooplankton density by sample location in Lake Norman 4-12 Figure 4-2 Lake Norman zooplankton densities among years 4-13 Figure 4-3 Lake Norman zooplankton composition in 1995 4-15 Figure 4-4 Lake Norman zooplankton density by group 4-16 V

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l Cil APTER I McGUIRE NUCLEAR STATION l OPERATIONAL DATA INTRODUCTION As required per the National Pollutant Discharge Elimination System (NPDES) permit number NC0024392 for McGuire Nuclear Station (MNS) issued by the North Carolina Department of Environment, Health and Natural Resources (NCDEHNR), the following annual report has been 1

prepared. This report summarizes environmental monitoring of Lake Norman conducted during  !

1995.

OPERATIONAL DATA FOR 1995 Monthly capacity factors of MNS during 1995 averaged over 50% for all months for both units except in December for Unit 1 (Table 1-1). During July, August, and September, when conservation of cool water and discharge temperatures are most critical, the thermal limit for

,r3 MNS increases from a monthly average of 95 F to 99 F. The average monthly discharge temperature was 94.4 F (34.7 C) for July,98.7 F (37.1 C) for August, and 94.7 F (34.8 C) for September 1995. Use of low level intake water was necessary in August 1995 for compliance with the thermal limit for MNS. Low level intake water was pumped only through the condenser of Unit 1 from August 22 - 30, 1995. The volume of cool water in Lake Norman is tracked throughout the year to ensure that an adequate volume is available to comply with both the Nuclear Regulatory Commission Technical Specification requirements and the NPDES monthly discharge water temperature limit.

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O T 8ie i-i. ^ver=#e - e ihir c P citr r cier- ( * > <=ic i <ea tre - a iir it e e ciir factors [ Net Generation (Mwe per unit day) x 100 / 24 h per day x 1129 mw i per unit l and monthly average discharge water temperatures for McGuire Nuclear Station during 1995.

t NPDES DISCHARGE CAPACITY FACTOR (%) TEMPERATURE i Month Unit 1 Unit 2 Statio- Monthly Average Average Average Average OF OC January 93.8 59.6 76.7 62.5 16.9 February 100.8 102.1 101:4 65.1 18.4 March 100.7 98.1 99.4 70.8 21.5 April 99.9 80.5 90.2 74.3 23.5 May 99.2 100.7 99.9 83.8 28.8 June 89.8 97.5 93.6 90.8 32.7 July 80.2 98.7 89.4 94.4 34.7 August 96.7 97.4 97.0 98.7 37 1 September 87.4 98.2 92.8 94.7 ~34.8 1 October 90.7 100.1 95.4 87.0 30.6 November 100.4 101.4 100.9 77. !

O December 39,3 69.5 54.4 65.1 25.1 18.4 I

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CHAPTER 2 WATER CHEMISTRY INTRODUCTION The objectives of the water chemistry portion of the McGuire Nuclear Station (MNS) NPDES Maintenance Monitoring Program are to:

l .1) maintain continuity in Lake Norman's chemical data base so as to allow detection of any i 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.

l l This year's report focuses primarily on 1994 and 1995. Where appropriate, reference to pre-1994 data will be made by citing reports previously submitted to the North Carolina Department of Environment. Health, and Natural Resources (NCDEHNR).

O unruons ^"o u^TExi^'s The complete water chemistry monitoring program, including specific variables, locations, depths, and frequencies is outlined in Table 2-1. Sampling locations are identified in Figure 2-1, whereas specific chemical methodologies, along with the appropriate references are presented in Table 2-2. Data were analyzed using two approaches, both of which were consistent with earlier studies (DPC 1985, 1987, 1988 a, 1989, 1990, 1991, 1992, 1993, 1994, 1995). The first method l-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 encompasses Locations I 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 oxygen i content, maximum whole water column and hypolimnion heat content, mean epilimnion and l hypolimnion heating rates over the stratified period, and the Birgean heat budget.

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Heat (Kcal/cm ) and oxygen (mg/cm 2 or mg/L) content of the reservoir were calculated according to Hutchinson (1957), using the following equation:

Lt = Ao-le f TO . Az e dz where; j 2

2 l Lt = reservoir heat (Kcal/cm ) or oxygen (mg/cm ) content l Ao = surface area of reservoir (cm2) l TO = mean temperature ( C) or oxygen content oflayer z 1 Az = area (cm2) at depth z dz = depth interval (cm) zo = surface zm = maximum depth RESULTS AND DISCUSSION Precipitation Amount Precipitation values in the vicinity of MNS in 1994 and 1995 were similar with a total annual rainfall of 47.1 inches in 1994 and 49.5 inches in 1995 (Figure 2-2). The highest total monthly rainfall in 1995 occurred in October with a value of 6.23 inches.

I' Temperature and Dissolved Oxygen Water temperatures measured in 1995 illustrated similar temporal and spatial trends in the back-ground and mixing zones (Figures 2-3,2-4). Water temperatures in the winter of 1995 were generally equal to or cooler throughout the water column, as compared to 1994, in both zones (Figure 2-3,2-4). The lone exception to this trend was observed in the mixing zone in February, where 1995 temperatures were 1-2 *C warmer than in 1994. This trend persisted in both zones until September when it was reversed and 1995 temperatures measured 1-3 C warmer throughout most of the water column than observed in 1994. The fall and early winter temperature differences observed between 1994 and 1995 can be partially explained by O .

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variability in sampling. The 1994 data were collected early in the months of November and December, whereas in 1995 data were collected in the middle of the month for both months.

Despite some seasonal and spatial variability in temperature data between 1994 and 1995, the 1995 temperatures were well within the historic range (DPC 1985, 1989, 1991, 1993. 1994, 1995).

Temperature data at the discharge location in 1995 were generally similar to that measured in 1994 (Figure 2-5) and historically (DPC 1985, 1987, 1988a, 1989, 1990, 1991, 1992, 1993, 1994, 1995). The warmest discharge temperature of 1995 occurred in August and measured 37.0 C, or slightly greater than the historic maximum,of 36.3 C measured in August,1991 (DPC 1992). Temperatures were appreciably less in December,1995 than in December,1994 because of plant inactivity on the day of sampling. Temperatures otherwise would be expected to be similar to 1994 Seasonal and spatial patterns of DO in 1995 were reflective of the patterns exhibited for temperature, i. e., generally similar in both the mixing and background zones (Figures 2-6 and 2-7). Winter, and spring DO values consistently ranged within 1.0 to 1.5 mg/L of the 1994 values O thro"s a o"< the weier ceiem= ie dota ze#ce. eea were weii witate the nieterie reese core 1985 1987, 1988 a, 1989, 1990, 1991, 1992, 1993,1994, 1995 ). As has been observed in previous years, summer DO values in 1995 were highly variable throughout the water column in both the mixing and background zones ranging from highs of 6 to 8mg/L in the surface waters to lows of 0 to 2mg/L in the bottom waters. In general, summer DO levels in 1995 were slightly less than measured in 1994 and similar to 1993 values. All values recorded in 1995 were well within the historic range (DPC 1985, 1987, 1988 a, 1989, 1990, 1991, 1992, 1993,1994, 1995).

Fall and early winter DO values were normally similar between the two years in both zones.

Some interannual differences were observed in the October, November and December data, and partially reflect variability in sampling schedule, as discussed earlier. Interannual differences in DO are common in Southeastern reservoirs, particularly during the stratified period, and can reflect yearly differences in hydrological, meteorological, and limnological forcing variables (Cole and llannon 1985; Petts1984).

The seasonal pattern of DO in 1995 at the discharge location was similar to that measured historically, with the highest values observed during the winter and lowest observed in the O 8"mmer ""a cerir-reii cri8"re 2-5). oe"ereiiv oo veiece i" 1995 were en""i to or 8' 8ativie88 2-3

O than 1994 values from late winter to late summer, and slightly greater than 1994 values during fall. All DO values measured in 1994 and 1995 were well within the historic range (DPC 1985, 1987, 1988a, 1989, 1990, 1991, 1992, 1993, 1994, 1995). The lowest DO concentration measured at the discharge location in 1995 (4.9 mg/L) occurred in July and was slightly less than the August,1994 low of 5.6 mg/L (Figure 2-5). This was comparable'with the NCDEHNR water quality standard for dissolved oxygen of 5.0 mg/L.

Reservoir-wide Temperature and Dissolved Oxygen The monthly reservoir-wide temperature and dissolved oxygen data for 1995 are presented in Figures 2-8 and 2-9. These data are similar to that observed in previous years and are characteristic of cooling impoundments and hydropower reservoirs in the Southeast (Cole and Hannon,1985; Hannon et. al.,1979; Petts,1984). For a detailed discussion on the seasonal and spatial dynamics of temperature and dissolved oxygen during both the cooling and heating periods in Lake Norman, the reader is referred to earlier reports (DPC 1992,1993,1994,1995).

The seasonal heat content of both the water column and the hypolimnion for Lake Norman in O i995 are grescoted ie ri 8ere 2-10e: edditio ei ieformetioe ou the thermai resime ie the rczervoir for the years 1994 and 1995 are found in Table 2-3. Anmial minimum heat content for the entire water column in 1995 (7.81 Kcal/sq cm; 7.8 C) occurred in early-February, whereas the maximum heat content (28.22 Kcal/sq cm; 27.9 C) occurred in mid-August. Heat content of the hypolimnion exhibited somewhat the same seasonal trend except that the maximum occurred in mid-September, or about three weeks later than observed for the entire water column. Minimum hypolimnetic heat content measured 4.77 Kcal/sq cm (7.5 C ), whereas the maximum was 16.04 Kcal/sq cm (24.5 C ). Heating of both the entire water column and the hypolimnion occurred at approximately a linear rate from minimum to maximum heat content. The mean heating rate of the entire water column equalled 0.105 Kcal/sq cm versus 0.052 Kcal/sq cm for the hypolimnion.

The 1995 heat content data were generally similar to that observed in 1994 and earlier years (

DPC 1992,1993,1994,1995 ).

The seasonal oxygen content and percent saturation of the whole water column and the hypolimnion are depicted in Figure 2-10b. Additional oxygen data can be found in Table 2-4 which presents the 1995 AHOD for Lake Norman and contrasts it with similar estimates for 18 TVA reservoirs. Reservoir oxygen content was greatest in mid winter when DO content O mee ered 10.5 m8/L for the wheie weter ceieme 10.4 m8/L for the hrneiimeiee. eerceet  !

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( saturation values at this time approached 93% for the entire water column and 88% for the hypolimnion. Beginning in early spring, oxygen content began to decline precipitiously in both the whole water column and the hypolimnion, and continued to do so in a linear fashion until reaching a minimum in mid summer. Minimum summer DO values for the entire water column measured 4.4 mg/L (57.4% saturation), whereas the minimum for the hypolimnion was 0.5 mg/L (5.8% saturation). The mean rate of DO decline in the hypolimnion over the stratified period, 2

i.e., the AHOD, was 0.042 mg/cm / day (0.090 mg/L/ day) (Figure 2-10b ).

Hutchinson (1938,1957) proposed that the decrease of dissolved oxygen in the hypolimnion of a waterbody should be related to the productivity of the trophogenic zone. Mortimer (1941) adopted a similar perspective and proposed the following criteria for AHOD associated

• 2 with various trophic states; oligotrophic- 5 0.025 mg/cm / day, mesotrophic- 0.026 2 2 2 mg/cm / day to 0.054 mg/cm / day, and cutrophic- 2 0.055 mg/cm / day. Employing these limits, Lake Norman should be classified as mesotrophic based on the calculated AHOD value of 0.042 2

mg/cm / day. The oxygen based mesotrophic classification agrees well with the mesotrophic classification based on chlorophyll a levels (Chapter 3). The 1995 AHOD value is also similar to that found in other Southeastern reservoirs of comparable depth, chlorophyll a status, and secchi O dev1h (Table 2-4).

l Striped Bass Habitat Suitable pelagic habitat for adult striped bass, defined as that layer of water with temperatures s 26 C and DO levels 2 2.0 mg/L, was found lake-wide from late September 1994 through early June 1995. Beginning in late-June 1994, habitat reduction proceeded rapidly throughout the reservoir both as a result of deepening of the 26 C isotherm and metalimnetic and hypolimnetic deoxygenation (Figure 2-11). Habitat reduction was most severe from 7 July to 9 August with no measureable habitat observed on 21 August. Temperature and dissolved oxygen measurements on 13 September revealed the presence of suitable habitat in the mid to upper portions of the reservoir. liabitat measured in the upper reaches of the reservoir appeared to be influenced by discharges from Lookout Shoals Hydroelectric facility which were somewhat -

cooler than ambient conditions in Lake Norman. Upon entering Lake Norman, this water l

apparently mixes and then proceeds as a subsurface underflow (Ford 1985) as it migrates downriver.

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O Phyeicechemicei hebitet wes eb erved to expend eggreciebiy in ie1e-Segtember p,imariiy es e result of epilimnion cooling and deepening, and in response to changing meteorological conditions. By 12 October suitable pelagic habitat for striped bass was measured reservoir-wide. l The temporal and spatial pattern of striped bass habitat expansion and reduction observed in 1995 was similar to that previously reported in Lake Norman and many other Southeastern I reservoirs (Coutant 1985, Matthews 1985, DPC 1992, DPC 1993,1994,1995). The duration of habitat elimination in 1995 extended from about mid-August to mid-September, or about one month and was well within the historic range. Only one dead striped bass >500mm was reported in 1995 during weekly habitat assessments by DPC personnel in the summer. These conditions were similar to that in 1994 when no mortalities of striped bass were reported by local fishermen or observed.

Turbidity and Specific Conductance Surface turbidity values were generally low at the MNS discharge, mixing zone, and mid-lake background locations during 1995, ranging from 1.4 - 27 NTUs (Table 2-5). Bottom turbidity values were also relatively low over the study period, ranging from 1.7-25 NTUs (Table 2-5).

O Tacee veiee, were 8imiier to taeee meeeerea ie 1994 (Tebie 2 5), and well within the historic range (DPC 1989,1990,1991,1992.1993,1994,1995).

Specific conductance in Lake Norman in 1995 ranged from 51 to 66 umho/cm and was similar to that observed in 1994 (Table 2-5) and historically (DPC 1989,1992,1993,1994, 1995). Specific conductance in surface and bottom waters was generally similar throughout the year except in late fall at several of the deeper locations when bottom waters averaged about 20- 40 umhos/cm higher than surface values. These increases in conductance were undoubtedly related primarily to the release of soluble iron and manganese from the lake bottom under anoxic conditions (Table 2-5). This phenomenon is common in both natural lakes and reservoirs that exhibit hypolimnetic oxygen depletion (liutchinson 1957, Wetzel 1975).

pli and Alkalinity -

During 1995, pli and alkalinity values were similar among MNS discharge, mixing and background zones (Table 2-5); they were also similar to values measured in 1994 (Table 2-5) and historically (DPC 1989,1992, 1993, 1994, 1995). Individual pil values in 1995 ranged from 6.3 O t 7.7 -acreee ei'eiieitr <=eaea crom 6 4 to 13 8 ma orceco1 2-6

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< U Major Cations md Anions The concentrations (mg/L) of major ionic species in the MNS discharge, mixing, and mid-lake background zones are provided in Table 2-5. The overall ionic composition of Lake Norman during 1995 was similar to that reported for 1994 (Table 2-5) and previously (DPC 1989,1992, 1993, 1994, 1995). Lake-wide, the major cations were sodium, calcium, magnesium, and potassium; major anions were bicarbonate, sulfate, and chloride.

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Nutrients Nutrient concentrations in the discharge, mixing, and mid-lake background zones of Lake Norman are provided in Table 2-5. Overall, nitrogen and phosphorus levels in 1995 were similar I to those measured in 1994 and historically (DPC 1989, 1990, 1991, 1992, 1993, 1994, 1995);

they are also characteristic of the lake's oligo-mesotrophic status. Ammonia nitrogen concentrations increased in bottom waters in each of the three zones during the summer and fall, concurrent with the development of anoxic conditions. Total and soluble phosphorus concentra-tions in 1995 were similar to values recorded in 1994 and historically (DPC 1989,1990,1991, .

O 1992 ,i993.1994,i995).  !

l Metals  !

l Metal concentrations in the discharge, mixing, and mid-lake background zones of Lake Norman  ;

for 1995 were similar to that measured in 1994 (Table 2-5) and historically (DPC 1989, 1990, 1991, 1992, 1993, 1994, 1995). Iron concentrations near the surface were generally low (s 0.1 mg/L) during 1994 and 1995, whereas iron levels near the bottom were slightly higher during the stratified period, particularly in early fall. Similarly, manganese concentrations in the surface and bottom waters were generally low (s 0.1 mg/L) in both 1994 and 1995, except during the summer and fall when bottom waters were anoxic (Table 2-5). This phenomenon, i.e., the release ofiron and manganese from the bottom sediments due to solubility changes induced by low redox conditions (Iow oxygen levels) is common in stratified waterbodies (Wetzel 1975). .

Manganese concentrations near the bottom rose above the NC water quality standard (0.5 mg/L) at various locations throughout the lake in summer and fall of both years, and is characteristic of historic conditions (DPC 1989,1990,1991,1992,1993,1994,1995). Heavy metal concentrations in Lake Norman never approached NC water quality standards, and there were no consistent O enereciesie airrereecce set-ece i994 eea i995.

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3 (U l FUTURE STUDIES No changes are planned for the Water Chemistry portion of the Lake Norman maintenance monitoring program during 1996 or 1997.

SUMMARY

Temporal and spatial trends in water temperature and DO data collected monthly in 1995 were j similar to those observed historically. Temperature and DO data collected in 1995 were within the range of previously measured values.

Reservoir-wide isotherm and isopleth information for 1995, coupled with heat content and hypolimnetic oxygen data, illustrated that Lake Norman exhibited thennal and oxygen dynamics characteristic of historic conditions and similar to other Southeastern reservoirs of comparable size, depth, flow conditions, and trophic status.

O a vaiiasiiits e r uiiebic veiesic hebitat fer edeit striged ba s ie take Nermaein 1995 wes generally similar to historic conditions. Reservoir-wide habitat elimination occuned for about a month in 1995. Tnese conditions were better than observed in 1993 but somewhat more restrictive than in 1994 when habitat was never elimniated in the reservoir. Only one dead striped bass >500m was reported in 1995.

All chemical parameters measured in 1995 were within the concentration ranges previously reported for the lake during both MNS preoperational and operational years. As has been observed historically, manganese concentrations in the bottom waters in the summer and fall of 1995 often exceeded the NC water quality standard. This is characteristic of waterbodies that experience hypolimnetic deoxygenation during the summer.

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( LITERATURE CITED l

Coutant, C. C.1985. Striped bass, temperature, and dissolved oxygen: a speculative hypothesis for environmental risk. Trans. Amer. Fisher. Soc. I14:31-61.

Cole, T. M. and H. H. Hannon.1985. Dissolved oxygen dynamics. In: Reservoir Limnology:

Ecological Perspectives. K. W. Thornton, B. L. Kimmel and F. E. Payne editors. John j Wiley & Sons. NY. l l

Duke Power Company.1985. McGuire Nuclear Station,316(a) Demonstration. Duke Power i Company, Charlotte, NC.

Duke Power Company.1987. Lake Norman maintenance monitoring program: 1986 summary.

Duke Power Company, Charlotte, NC.

Duke Power Company.1988a. 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. j Duke Power Company, Charlotte, NC.

Duke Power Company.1990. Lake Norman maintenance monitoring program: 1989 summary.

Duke Power Company, Charlotte, NC. ,

1 Duke Power Company.1991. Lake Norman maintenance monitoring program: 1990 summary.

Duke Power Company, Charlotte, NC.

Duke Power Company.1992. Lake Norman maintenance monitoring program: 1991 summary.

Duke Power Company, Charlotte, NC.

Duke Power Company.1993. Lake Norman maintenance monitoring program: 1992 summary.

Duke Power Company, Charlotte, NC.

Duke Power Company.1994. Lake Norman maintenance monitoring program: 1993 summary.

Duke Power Company, Charlotte, NC. ,

Duke Power Company.1995. Lake Norman maintenance monitoring program: 1994 summary.

Duke Power Company, Charlotte, NC.

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i i

O eerd D. e.1985. Reserveir transgert grecessee. in: Re ervoir Limnoiesy: Eceiosicei Perspectives. K. W. Thornton, B. L. Kimmel and F. E. Payne editors. John Wiley &

Sons. NY. 1 Hannan,11. H.,1. R. Fuchs and D. C. Whittenburg.1979 Spatial and temporal patterms of temperature, alkalinity, dissolved oxygen and conductivity in an oligo-mesotrophic, deep-storage reservoir in Central Texas. Hydrobilologia 51 (30);209-221.

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.1938. Chemical stratification and lake morphometry. Proc. Nat. Acad. Sci.,

24:63-69.

I Hutchinson, G. E.1957. A Treatise on Limnology, Volum.e I. Geography, Physics and l Chemistry. John Wiley & Sons, NY. I Hydrolab Corporation.1986. Instructions for operating the Hydrolab Surveyor Datasonde.

Austin, TX. 105p.

Matthews, W. J., L. G. Hill, D. R. Edds, and F. P. Gelwick.1980. Influence of water quality and season on habitat use by striped bass in a large southwestern reservoir. Transactions ,

of the American Fisheries Society 118:243-250.

Mortimer, C. H.1941. The exchange of dissolved substances between mud and water in lakes (Parts I and II). J. Ecol.,29:280-329.

Petts G. E.,1984. Impounded Rivers: Perspectives For Ecological Management. John Wiley and Sons. New York. 326pp.

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. .

Stumm, w. and J. J. Morgan.1970. Aquatic chemistry: an introduction emphasizing chemical equilibria in natural waters. Wiley and Sons, Inc. New York, NY 583p.

Wetzel, R. G.1975. Limnology. W. B. Saunders Company, Philadelaphis, Pennsylvania, 743pp.

O 2-10

- _ . . _ _ _ _ . _ _ _ _ __ _m _m _.

~

\

l t

4 Table 2-L Water chemistry program for the McGuire Nuclear Station NPDES long-term maintenance monitonng m Lake Norman-WOUlltBNPDHS SAMPLEG PROGRAM SemP t e Cou*o Seedule for 1995 PARAMETEllS LOCATIONS 1.0 2.0 4.0 5.0 S.0 9.5 11 0 13,0 14 0 15.0 15.9 62.0 69.0 710 30.0 16.0 DEPTH (m) 33 33 5 20 32 23 27 21 to 23 23 15 7 5 4 3 SAM CODE D&STTUANALYSIS Temparurure Hydrolab Dienolved Ongen Hydrolsb In-esta --__ _te are entlected monthly er the above locations at lm intervals from 0.3m to im above bettant pH Hydrolah Measurements are taken weekly Troep Ady Augun for striped bens habitat Conductrrity Hydrolab NtfTitL'NT ANALYSES Ammotus AA-Nut Q/T,B Q/T.B Q& Q/T.B Q/T,B Q/T.B Q/T.B Q/T.B Q/T Q/T.B Q/T,B S/T Mirate+Mmte AA-We Q/TE Q/T.B Q/T Q/T B Q/T.B Q/I.B Q/T.B Q/T,B Q/T Q/T.B Q/T,B S/T Onhophosphate AA We Q/T.B Q/T.B Q/T Q/T.B Q/T.B Q/T B Q/TB Q/T.B Q/T Q/I,B Q/T.B S/T ,

Total Phearborne AA-TP DG-P Q/T,B Q/T.B QT Q/T.B Q/T.B Q/T,B Q/TE Q/T,B Q/T Q/T.B Q/T,B S/T Sihce AA-Nut Q/I.B Q/T.B Q/T Q/T,B Q/T,B Q/T.B Q/T.B Q/T.B Q/T Q/T.B Q/T B S/T C1 AA-Nut Q/T,B Q/TB Q/T Q/T.B Q/T,B Q/T,B Q/T,B Q/T,B Q/T Q/T.B Q/T B S/T TKN AAlTN S/T,B S4,B tHEMTNTAL ANAL YSES Alonunum ICP 24 QT,B S/T.B S/T Q/T,B Q/T B Q/T.B Q/T,B Q/T,B Q/T Q/T.B Q/T.B S/T Calcmm ICP 24 Q/T.B Q/T.B Q/T Q/T.B Q/T.B Q/T.B Q/T,B Q/T,B Q/T Q/T B Q/T,B S/T Irom ICP 24 QT.B Q/T.B Q/T Q/T,D Q/T.B Q/T.B Q/T.B Q/T.B Q/T Q/T.B Q/T,B S/T I[ Q/T,B Q/T,B Q/T,B Q/T,B Q/T,B S/T

- M.es um ICP-24 Q/T Q4.B Q/T.B Q/T B Q/T Q/T.B

- Merpuene ICP-24 Q/T.B Q/T.B Q/T Q/T.B Q/T.B Q/T B Q/T,B Q/T,B QT Q/T.B Q/TB 3/T Potammum 306-K Q/T B Q/IB Q/T Q/T.B Q4E Q T.B Q/T,8 Q/T B Q/T Q/T.B Q/T,B S/T Sodmm ICP-24 Q/T,B Q/T B Q/T Q/T.B Q/T.fi Q/T.B Q/T,B Q/T.D Q/T Q4,B - Q/T,B S/T Zac ICP-24 Q/T,B Q/T.B Q/T Q/T,B Q1.t1 Q/T.R Q/T.B Q/T,B Q/T Q/T.B Q/T,B S/T CmJnenum IIGA-CD S/T,B S/T S/J.B S/T.D S/T SS.B S/T Cog 7er IIGA-CU S/T.B S/T S/T B " S/T.D S/T S/T.B S/T Lees IIGA-PB S/T,B $6 S/T.B S/T B S/T S4,8 S/T ADDT1 TONAL ANALYSBS Alkuluuty T-ALIT Q/T,B Q/T.B Q/T Q/T,B Q/T,B Q/TB Q/T.B Q/TB Q/T Q/T.B Q/T B S/T Turbidary F-TUllB Q/T,B Q/T.B Q/T Q/T.B Q/T.B Q/T,B Q/T B Q/T.B Q/T Q/T,B Q/T.B S/T Su1 Tere LA/SO4 S/T B S/T S/T,B S/T S/T.B S/T Total Sohds S-TSE S/T,B S/T S/T.B S/T S/T,B S/T Tor =1 Suspended Solid 3-TSSE S/T,B S/T 3/T.B S/T S/T.B S/T CODES: Freper:cy Q = Quarterly (Feb, May, Aug, Nov) S = Seou-ensually (Feb,A qn T = Top (0.3m) B = Bonom (tm above bottom) e

- - - - - - - - - - - . _____._____a-. . . _

~

O Table 2-1. Water chemistry program for the McGuire Nuclear Station NPDES long-term mair.teanoce :nmitoring an Lake Norman, 1&OUDtBNPDES SAMPUNO PROGitAM Sample CcHection Schedule for 19M PARAhEERS LOCATIONS 1.0 2.0 4.0 5.0 S.0 9.5 11.0 13.0 14.0 15.0 15,9 62.0 69.0 110 30.0 16.0 DEPTH /m) 33 31 5 20 32 23 27 21 10 23 23 15 7' 5 4 3 SAM CODB DMTRUARALYSIS Temrerature . Hydroleb Dumotved Oxygsa Hydraleb In-ems _ ____te are couected monthly at the abovelocatiora et le istervais from E3m to la above botesen pH Hydrolab Measuremente are taken weekly from Ady August for etnped been liabitmL Conductmry Hydrolab Nin?!!NT ANALYSE 3 nmotus AA-Net Q/T B Q/T.B Qfr Q/T.B Q/T B Q/T,B Q/T,B Q/T,B Q.T Q/T.B Q/T.B Sfr Nitrate +Nitnte AA-Net Q/T,B Q/T.B Q/T Q/T B Q/T.B Qff,B Qff,B Q/T,3 Q4 Q/T,B Q/T,B S/T Orthophosphet. AA-Nut Q/T B Q/T,B Q/T Q/T B Q/T.B Q'T,3 Q/T B Q/T.B Q/T QS B QffE S/T Teud Phosphonse AA 17,DG-P Q/T.B . Q/TB Q/T Q/T,B Q/T.B Q/T,D Q/T.B QJ.B Q/T Q/T.B Q/T,B S/T Sdism AA-Nut Q/T,8 Q4,B Q/T Q/T,B Q/T.B Qff,B Q/T B Q'T,B Q/T Q/T,B Q/T.B S/T Cl AA-Nut Q/T.B Q/T,B Q/T Q/T.B Q/T,B Q/T,B Q/T.B Q/T,B Q/T Q'T,B Q/T,B $4 TKN AA-TKN Sff,B S/T.B F2 DENTAL AN ALYSF'1 Alununum ICP-24 Qff,B S/T,B S/T Q/T B Q/T.B Q/T,3 Qfr,B Q/T,B QIT Q6,B Q/T.B $/T Calemm ICP-24 Q/T.B Q/T.B Q/T Q/T.B Q/T.B Q/T.B Q/T,B Q/T.B ' Q/T Q&,B Q/T,B ET Q/T,B Q/T,B Q/T,B Q/T,8 Q/T,B Q/T,B Q/T B Q/T Q/T.B Qfr B S/T t,J 1,em ICP-24 Q/T Q/T,B S/T Mesmoum ICP-24 Qfr,B Q/T B Q/T Q/T.B Q/T B Q'T,B Q/T B Q/T,D Q/T Q/T B

- hemmene ICP-24 Q/T.B Q/T.B Q/T Q/T.B Q/T D Q/TE Q/T,B Q/T,B -Q6 Qff,B Q/T,B S/T Potamnum 306-K Q/T.B Q/T,B Q/T Q/T B Q/T,B Q/T,ll Qff,B Q/T,B Q/T Q/T,B Q/T B S/T Se&um ICP-24 QfT,B Q/T,B Q/T Q/T,B Q/T.B Q/T.B Q/T.B Q/T,B Q/T Q/T.B - Q/T,B S/T Zinc ICP-24 Q/T,B Q/T,B Q/T Q/T,B QfLD Q/T D Q/T,B Q/T.B Q/T Q/T B Q4,B S/T C=damiina IIGA-CD Sff,B S/T Sff,B 3/T D S,T S/T,B S/T IIGA-CU Sff,B 3/T S/T,B " S/T,B S/T SfT,B S/T Ces ier Sff L HGA-PB SS,B S/T SSE Sff,B S/T S/T,B ADDTT10NAL ANALY":E3 Namimity T ALIT Q/T.B Q/TB Q/T Q/T B Q/T B Q/T.B Q/T B Q/T,B Q/T Q/T,B QfT,B Sff Turb dary F-TURB Q/T.B Q/T,B Q/T Q/T,B Q/T.B QJ.B Q6.B Q/T,B Qfr Q/T,B Q/T,B S/T sulfate tN SO4 S/T.B Sfr S/T,B S/T S/T B Sfr Total Sohde S TSE 3/T.B S/T S/T,B S/T S/T,B S/T Tee =1 Simpauled sohd S-135E S/T,B S/T SS,B S/T S/T,B Sfr CODES. Frequency Q = Quarterly (Pets May, Aug, Nov) S = Sean-nanually (Feb,Aug)

T = Top (0.3m) B = Bottom (Im above bottom) 4 r

4

_ _ _ _ . _ _ - . 1__ _ _ . _ _ _ - .

_ _ _ _ _ _ _ _ _ _ _ - - - - . s

~

O O si Table 2-2. Water chemistry methods and analyte detection limits for the McGuire Nuclear Station NPDES long-term maintenance program for Lake Norman.

Preservatten Detectfen timft t Variables *I Methed i

.Img-CACO 1-5* i Electrometric titration to a pH of 5.I' 4*C 11Lattnity. total  !.'  ;

O.5% HNO, 0.3 mg.1-8 Al e.tnum Atomic emission /ICP-direct injection' i 4*C 0.050 m gl-*

A ontum Automated phenate' O.5% HNO, 0.1 99 1-8 [

C a ds t u.m Atomic' absorption / graphite furnace-direct inje.ction' O.5% HNO, 0.04 mg 1-5 Caletus Atomic' emission /ICP-direct injection' 4*C 1.0 mg 1 5  !

Chloride Automated ferricyanide'

^

In-situ 1 umho cm-8* l Cencuctance, spectftc Temperature compensated nickel electrode' 8 0.5%HEO, 0.5 99 1 8 l Cc cer Atomic absorption / graphite furnace-direct injection 4'C 0.10mg.1

• Fluoride Potentiometric'

• O.5% HNO, 0.'l mg 1-8 1ren Atomic emission /ICP-direct injection'

-0.5% HNO, 2.0 ug l'I-  ;

Lead Atomic absorption graphite furnace-direct injection' O.5% HNO, 0.001 mg 1-'

Magnestum Atomic emission /ICP-direct injectten' .

O 5% HNO, 0.003 mg 1-'

ia

• Manganese Atomic emission /ICP-direct injection' 4*C . 0.050 mg.1-* i

' Nitrite

• Nitrate Automated cadmlum reduction' -

4*C 0.005 mg.1-'

Orthochosphate Automated ascorbic acid' reduction, '

8*

in-situ O.1 mg 1 ,

0xygen, dissolved Temperature compensated polarographic cell'  !

Temperature compensated glass electrode' In-situ 0.1 std. units *

H -

4*C 0.005 mg 1-  !

Phosphorus. total Persulfate digestion followed by autoaated ascorbic acid 0.015 mg 1- *"

reouction' -

i Atomic absorption graphite furnace-direct lajection' O.5% HNO, 0.1 mg 1 Potassium 4*C 0.5 mg 1 5fisca Automated molydostlicate' Atomic emission /ICP-direct injection' O.5% HNO, 0.3 m gl-*

Sectum 4*C 1.0 mg 1-8 Sulfate Turbidimetric, using a spectrophotometer' In-situ 0.l*C' Te ;erature Thermistor / thermometer' 4*C 1 HTU*

Turbidtty Hephelometric turbidity' Atomicemission[lCP-directinjection' O.5% HHO, 4991 Zine

' United States Enytronmental Protection Agency 1979. Methods for chemical analysis of water and wastes.

Environmental Monitoring and Support Laboratory. Cincinnatt. OH.

t

'USEPA. 1982..

'USEPA. 198a

• Instrument sensitivity used instead of detection limit.

' Detection Itmit changed during 1989

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

i .

l O rasie 2 3. lieat content calculations for the thermal regime in Lake Norman in 1994 and 1995.

b

{ 1994 1995 4

Maximum areal heat content ( g cal /cm') 27,873 28,215 2

j Minimum areal heat content (g cal /cm ) 7,336 7,808

, Maximum hypolimnetic (below 11.5 m) 15,130 16,036 1 arealheat content (g cal /cm )

Birgean heat budget (g cal /cm*) ' 20,537 20,407 i

Epilimnion (above 11.5 m) heating O.138 0.I11 rate (C/ day)

O 1

Hypolimnion (below 11.5 m) heating 0.105 0.103 i rate (C/ day) i e

4 4

l a

i O -

i 2-13

O Table 2-4. A comparison of areal hypolinuietic oxygen deficits (AHOD), summer chlorophyll a (chi a), secchi depth (SD), and mean depth of Lake Norman and 18 TVA reservoirs.

l AHOD Summer Chi a Secchi Depth Mean Depth l Reservoir (mg/cm2/ day) (ug/L) (m) (m) >

Lake Norman 0.042 6.02 1.7 10.3 I

TVAa  ;

Mainstem )

Kentucky 0.012 9.1 1.0 5.0  !

Pickwick 0.010 3.9 0.9 6.5 l Wilson 0.028 5.9 1.4 12.3 l Wheelee 0.012 4.4 5.3 Guntersville 0.007 4.8 1.1 5.3 Nickajack 0.016 2.8 6.8 O Chickamauga 0.008 3.0 1.1 1.1 5.0 Watts Bar 0.012 6.2 1.0 7.3 Fort London 0.023 5.9 0.9 7.3 Tributary Chatuge 0.041 5.5 2.7 9.5 Cherokee 0.078 10.9 l.7 13.9 Douglas 0.046 6.3 1.6 10.7 Fontana 0.113 4.1 2.6 37.8 Hiwassee 0.061 5.0 2.4 20.2 Norris 0.058 2.1 3.9 16.3 ~ .

South Holston 0.070 6.5 2.6 23.4 Tims Ford 0.059 6.I 2.4 14.9 Watauga 0.066 2.9 2.7 24.5 A Data from Higgins et al. (1980), and Higgins and Kim (1981)

O .

2 14

w -

A f

I I

Tab!e 2 5 Quarterfy surface (0.3 m) and botom (bottom minus 1 m) water chemistry for the MNS discharga, mbdng zone, and background locations on Lake Norman during 1994 and 1995. Vatues less than detection were assumed to be tr e detection limit for calculating a mean.

Mixino Zone MMnD Zone MNS DischarDe Mbdng Zone Backgrotrid Backgrotrid '

LOCATION: 1.0 2.0 4.0 5.0 8.0 11.0 CEPTH: Surface Bottom Surface Bottom Stsface St.rface Bottom Stahce Bottom Sufaco Bottom PWMETERS YEAR: 94 95 94 95 94 95 94 95 94 P5 94 95 94 95 94 95 94 95 94 95 94 95 la teory (ntu) ,

Feb 2 5.4 4 4.7 3 4.9 4 6.6 3 4.7 3 4.6 4 5.4 3 6.7 . NS 84 6 27 8 25 May 2 2.4 3 8.4 2 2.6 5 7.9 2 2.6 2 2.6 7 7.6 2 2.9 9 8.4 3 2.4 14 9.2 Aug 4 2.3 17 13.1 5 1.8 10 7.7 2 1.87 2 6.9 5 2 2 2.3 4 16.9 5 2.3 7. 13.3 Nov 4 38 6 1 67 3 1.67 6 4.7 4 33 3 32 8 1.9 3 1.4 9 1.7 3 22 to

• 36 Annual Mean 3 3.475 7.5 6 97 3 25 2.74 6.25 6.73 2.75 3.12 2.5 4 33 6 4 23 2.5 3.33 7.33 8.85 4 25 8.48 9 75 12 8 SpeMc Conouctance (umno/cm) .

Feb 63 58 66 58 NS $8 NS 58 64 59 59 59 60 58 68 57 72 57 76 51 76 52  !

May 66 54 67 51 66 54 67 51 66 55 66 54 68 52 66 54 65 51 63 53 64 51 t Aug 65 62 80 68 65 62 80 64 64 62 E5 62 80 82 64 62 77 67 64 62 75 71 Nov 55 56 92 56 56 56 61 56 57 57  !$ 57 56 56 55 56 55 56 54 53 57 52 .

Annum Mean 62 3 57 5 76 3 58 3 62 3 57,5 69 3 57.3 ti2 8 58.3 61.5 58 66 62 63.3 57.3 67.3 57.8 64 3 54 8 68 56 5 mts)

Feb 7.6 7.5 68 7 NS 7.7 NS 6.9 6.9 7.1 6.8 7.2 6.9 6.9 6.9 7.6 6.8 6.8 7 7.3 68 6.7 May 6.9 66 66 6.3 6.9 6.8 65 6.3 6.5 6.7 6.8 6.8 6.6 6.3 7.1 7.1 6.5 6.3 8 7.1 6.5 6.2 ,

J Aug 6.7 6.6 6.4 6.4 6.8 6.7 6.3 6.3 6.5 6.5 6.7 6.7 62 6.5 7 6.9 6.4 6.3 7.5 6.9 6.3 6.4 '

L Nov 72 63 66 67 7 68 66 6.8 69 6.6 7.1 69 6.6 68 7.4 6.8 64 6.8 7.3 68 65 65 A Annual Mean 71 6 75 66 66 69 7 6 47 6 58 'I73 6.73 6 68 6.9 6.58 6 63 7.1 7.1 6 53 6 55 7.45 7.03 6 53 6 45 Ae aWy (mc CACO 34)

Feb 13.1 12.5 13 6 10 5 13.2 11 12.7 9.5 12 11 12.4 9.5 12.9 10 13.4 to NS 9.5 13.9 8.5 14.5 10.5 May 11.6 10 11.7 95 12 8 11.5 8 11.7 9 12 95 11.8 9 11.5 7 12.1 9 11.5 to 11.5 10.5 i Aug 12.5 6.5 16.5 8.7 12.2 6.6 17 7.7 12 9 6.8 12.6 5.6 13.3 8.2 12.4 6.4 13.8 9.6 12.9 6.7 13 94  ;

Nov 14 2 13 35 14 6 13 9 12 6 14 13 6 13 6 12.4 13.5 12.4 13.7 12 6 13 8 12.4 13.8 12.4 13.7 12.1 12 6 12 4 12.2 f Annum Mean 12 9 to 59 14 1 10.7 12.5 9.9 13 7 97 12.3 10.1 12.4 9 23 12.7 10.3 12.4 9.3 12.8 10.5 12 6 9 45 12 9 to 7 CNorce (mg1) -

Feb 6.1 5.3 6.8 5.4 6.6 6 6.7 5 6.5 5.5 5.5 7.1 5.5 5.5 6.5 5.4 NS 5.5 8.4 4.9 8 5 i May 5.7 4.9 5.8 4.6 7.4 4.7 6.1 4.5 6.1 4.6 6.3 4.7 6.2 46 6.5 4.8 6.2 4.4 5.2 4.5 4.4 4.2 Aug 6.3 5.3 7.3 4.3 6 5.6 6.2 4.6 7.7 5.2 6.7 5.4 5.6 5.1 7 5.3 7 4.7 6 5.3 6.2 4.3 .

Nov $8 55 59 5.7 57 5.5 59 56 6 57 59 5.7 6 6.2 6 56 6 5.7 5.7 52 63 5.3 l Annum Mean 59S 5.25 6 45 5 6.43 5.45 6 23 4.93 6.58 5.25 6.1 5.73 5.83 5.35 65 5.28 6.4 5.08 6 33 4 98 6 23 4.7 ,

S# ate (mg1) i Feb NS NS NS NS 6.7 4.95 7.7 5.31 7.2 5.83 NS NS NS NS 7.4 5.48 NS 5.31 NS NS NS NS  ;

Aug NS NS NS NS 5 6 58 4 8.06 43 7.49 NS NS NS NS 4.3 7.49 5.1 9 02 NS NS NS NS Annual Meon 5.85 5 77 5.85 1569 5.75 6.65 5.85 6.49 5.1 7.17 Caien.un (mg1)

Feb .NS 2.659 NS 2.66 NS 2.66 NS 2.66 NS 2.67 NS 2.66 NS 2.66 NS 2.67 NS 2.69 NS 2.58 NS 2.62 May 2.7 2 724 2.8 2.79 2.8 2.73 2.9 2.79 2.8 2.72 2.8 2.73 2.9 2.2 2.8 2.7 3 2.82 2.7 2 91 3 2.83 Aug 28 2.811 3.3 3.31 2. 8 2.83 3.4 3.2 2.9 2.82 2.9 2.88 3 3.04 2.7 2.79 3 3.43 2.9 2.88 3 3.52 Nov 29 2 647 3 2 68 2.8 2 62 2.9 2.67 28 2 64 2.8 2 65 2.8 2 65 2.8 2 65 2.7 2.66 2.7 24 27 2 41 Annual Mean 28 2 727 3 03 2.86 28 2.71 T OI 2.83 2.83 2.71 2.83 2 71 2.9 2.79 2.77 2.7 2.9 2.9 2.77 2 69 29 2 85 v a r e s.um tmg.ij Feb NS 1.193 NS 1.99 NS 1.2 NS 1.19 NS 1.19 NS 1.2 NS 1.21 NS 1.18 NS 1.17 NS 1.08 NS 1.1 May 1.3 1.189 1.3 1.18 1.3 1.18 1.3 1.18 1.3 1.16 1.3 1.18 1.3 1.18 1.3 1.16 1.3 1.18 1.3 1.19 a.2 f.18 Aug 1.2 1.264 1.3 1.35 1.2 1.27 1.4 1.32 1.3 1.26 1.3 1.25 1.3 1.31 1.2 1.27 1.3 1.38 1.3 1.28 1.3 1 41 Nov 1.3 1 269 1.3 1.27 1.3 1.26 1.3 1.27 1.3 1.26 1.3 1.27 1.3 1.27 1.3 1.26 1.3 1.27 1.3 1 21 13 121 l Annusf Mean 1 27 1 229 1.3 1 45 1.27 1.23 1.33 1.24 1.3 1.22 1.3 1.23 1.3 1.24 1.27 1.22 1.3 1.25 1.3 1.19 1.3 1 22 NS = Not Sampled

O ~

G v J Tac'e 2-5. (Continued)

Midng Zone MMnD Zone MNS Dscharge MMnD Zor e Backgrouid Backgromd LOCATION. 1.0 2.0 4.0 5.0 8.0 11.0 DEPTH: Sur+ ace Bottom Sutace Bottom Sufsce Suface Bottom Suface Bottom Sur* ace Ect*om aa.avETERS YEAR 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95

& cta ss.um tmol)

Feb 16 1.62 1.6 1.6 NS 1.6 NS 1.6 NS 1.62 1.5 1.63 1.5 1.6 NS 1.58 NS 1.59 1.7 1.59 1.6 1.59 May 1.7 1 62 1.3 1.59 1.4 1.55 1.5 1 61 1.4 1.58 1.4 1.59 1.5 1.57 1.5 1.57 1.5 1.59 1.4 1.46 1.5 1.5 Aug 15 1.53 1.5 1.65 1.5 1.55 1.5 1.55 1.5 1.59 1.5 1.56 1.5 1.57 1.5 1.58 1.5 1.61 1.5 1.5 1.5 1.6 Nov 29 1 72 16 1 68 1.7 1 67 16 1 CS 16 1 66 1.6 1 68 16 1.7 1.7 1.7 1.6 1.66 1.7 1.7 17 1 76 Amual veen 1 93 1 635 15 1 63 1 53 16 1.53 1 61 1.5 1.61 1.5 1.62 1.53 1 61 1.57 1 61 1.53 1.61 1.58 1 56 1 58 1 61 Sochum (mg1)

Feb NS 5.48 NS 5.38 NS 5.22 NS 5.17 NS 5.18 NS 5.17 NS 1.6 NS 4.99 NS 4.89 NS 3.9 NS 1.59 May 5.5 4 42 5.5 4.34 5.7 4.3 58 4.2 56 4.16 5.6 4.56 5.8 4.1 5.8 4.42 5.7 4.46 4.8 4 5.2 3 94 Aug 47 5.25 4.6 4.5 4.9 5.32 5.1 4.36 4.9 5.4 4.6 5 02 4.4 4.96 46 5.21 4.7 4.44 45 5.33 4.5 4 69 Nov 57 5 01 56 4 96 53 4 96 55 5 16 55 5.3 53 5 26 54 5.11 52 5 33 5.2 49 55 4 84 54 4 62 Annuai Mean 53 5 04 5.3 48 5.3 4.95 5 47 4 73 5 33 5.01 5.17 5 5.2 3.94 5.2 4 99 5.2 4 67 4 93 4 52 5 03 3 71 Aumnum (mgi) ,

Feb NS NS NS NS NS 0.23 NS 0.26 NS 0 24 NS NS NS NS NS 0.35 NS 0.27 NS 0.51 NS 0.48 May 0.1 NS 0.1 NS 01 0.14 0.1 0.37 0.1 0.18 0.1 NS 0.1 NS 0.1 0.14 0.1 0.29 < 0.1 0.14 0.2 0.23 Aug = 0.1 0.085 < L.1 0.11 < 0.1 0.08 < 0.1 0.08 = 0.1 0.07 < 0.1 0.09

• 0.1 0.1 < 0.1 0.07 = 0.1 0.09 < 0.1 0.1 = 0.1 0.12 Nov < 01 NS < 0.1 NS < 0.1 0.09 < 0.1 0.1 < 0.1 0 09 < 01 NS

• 0.1 NS _ < 0.1 0.14

• 0.1 0.11 < 01 0.11 01 0.12 Amust Mean < 01 0 035 < 0.1 0,11 < 0.1 0.13 = 0.1 0.2 < 0.1 0.15 < 0.1 0.09 < 0.1 0.1 = 0.1 0.17 4 0.1 0.19 e 0.1 0 21 0.13 0 24 won pg1)

Feb NS 0.137 NS 0.13 NS 0.11 NS 0.14 NS 0 13 NS 0.12 NS 0.14 NS 0.19 NS 0.17 NS 0.33 NS 0.35 IJ May 0.1 0 073 0.1 0.19 e 0.1 0.06 0.1 0.2 < 0.1 0.07 < 0.1 0 03 0.1 0.17 e 0.1 0.05 0.2 0.18 e 0.1 0.06 02 0.16 i Aug 0.1 0.029 0.5 1.1 < 0.1 0.03 0.7 0.65 < 0.1 0.04 4 0.1 0.03 0.1 0.7 < 0.1 0.03 0.2 1.4

• 0.1 0.03 0.1 1.13 Ch Nov < 01 0 065 02 0 85 < 0.1 0 06 0.1 0.09 < 0.1 0 07 < 0.1 0 06 0.2 0.12 < 01 0 07 02 0 09 < 01 01 02 0 14 AmusI Mean = 01 0 076 0 27 0 57 < 0.1 0.07 0.3 0.27 < 0.1 0.08

• 0.1 0 07 0.13 0.28 < 0.1 0.08 0.2 0.46 e 0.1 0.14 0 17 0 45 Mangenese (mpi)

Feb NS 0013 NS 0.01 NS 0.01 NS 0.01 NS 0.01 NS 0.01 NS 0.02 NS 0.01 NS 0.02 NS 0 03 NS 0.03 May 0 01 0.009 0.01 0.03 0.01 0.01 0.03 - 0,03 0.01 0.01 0.01 0.01 0.06 0.03 0.01 0.01 0.05 0.03 < 0.01 0 01 0.07 0.03 Aug 0 02 0 023 1.54 1.69 0.02 0.03 1.63 1.31 0.05 0.06 0.03 0.04 0.4 0.93 0.02 0.03 0.41 1.79 0.02 0.06 0.27 2.36 Nov 0 04 0 029 0 78 0 03 0 05 0.03 0 42 0.03 0 05 0 03 0.04 0 03 0.15 0 05 0.03 0.03 0.23 0 03 0 04 0 04 0 16 0 06 Annual Mean 0 02 0 02 0.78 0 44 0.03 0.02 e.71 0 35 0.04 0.03 0 03 0.02 0.2 0.26 0 02 0 02 0.23 0 47 0 02 0 03 017 0 62 Oacmum tug 1)

Feb NS NS NS NS NS < 0.1 NS e 0.1 NS 4 0.1 NS NS NS NS NS

• 0.1 NS

• 0.1 NS NS NS NS Aug NS NS NS NS < 01< 0.1 < 0.1 < 0.1 < 0.1 < 01 NS NS NS NS < 0.1 < 0.1 < 0.1 < 0.1 NS NS NS NS Annual Mean < 0.1 < 0.1 < 0.1 < 0.1 < 0.1 < 0.1 < 0.1 < 0.1

• 0.1 < 0.1 Copper (ugi)

Feb NS NS NS NS 1.3 1.5 1.9 2 2 1.5 NS NS NS NS 1.6 2 NS 1.6 NS NS NS NS Aug NS NS NS NS 2.4 2.1 08 1 63 1.4 1.26 NS NS NS NS 2.4 1.16 1.1 1.63 NS NS NS NS AnnualMean 1.85 1.8 1.35 1.82 1.7 1.38 2 1.58 1.1 1.62 Leaa (vg1)

Feb

• NS NS NS NS NS < 2 NS < 2 NS < 2 NS NS NS NS NS

• 2 NS < 2 NS NS NS NS Aug NS NS NS NS < 2< 2 < 2< 2 < 2< 2 NS NS NS NS < 2< 2 < 24 2 NS NS NS NS Annual Veen < 24 *2 < 2= 2 < 2= 2 < 2< 2 < 2< 2 Inc r.ugt)

Feb NS < 0.005 NS 0.01 NS < 0.01 NS

• 0.01 NS < 0.01 NS < 0.01 NS

• 0.01 NS

• 0.01 NS

• 0.01 NS < 0.01 NS < 0.01 May = 5< 0.005 = 5< 0.01 < $ 0.01

• 5< 0.01 < 5< 0.01 < 5< 0.01 < 5< 0.01 < 5 * . 0.01 < 5< 0.01 < 5< 0.01 < $< 0.01 Aug 7 0 006 = 5* 0.01 6< .0.01 7< 0.01 7* 0.01 20 < 0.01 6< 0.01 42 < 0.01 < 5< 0.01 25 4 0 01 = 5< 0 01 Nov < $< 0005 < 5< 0 01 < 5= 0 01 < 5= 0 01 < 5= 0 01 < 5 e 201,, a 5< 0.01 < $< 0.01 < 5< 0 01 < $< 0 01 < 5< 0 01 Amuel Mean 5 67 0.005 < 5= 0.01 5.33 < 0.01 5.67 < 0.01 5.67

• 0.01 10 < 0.01 5.33 = 0.0t 17.3

• 0.01

• 5* 0 01 11.7

• 0.01 < $< 0 01 NS = Not Sampled

_ . _ _ . . . _ . - m _ ...m - . . _ ._ ...._.. . . _ . . - - _ . _

. -.m _. . . . .

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7able 2-5 (Continued) i Mndng Zone Maing Zone MNS D!scharge Mhdng Zone Backgrotmd Background LOCA710N: 1.0 20 4.0 5.0 8.0 11.0 '

DEPTH: Surface Bottom Suface Eattc>m Str9mco Sur9 ace Bottom Stsface Boeom Suface Bottom PARAMETERS YEAR- 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 94 95 Nmate tugt)

Feb 302 240 329 230 352 260 243 240 229 250 210 250 212 230 245 260 NS 280 320 310 325 310 F May 307 250 335 410 305 260 390 380 315 270 307 200 355 380 286 260 418 390 260 250 237 330 Aug 140 90 250 140 140 90 190 230 143 90 140 50 200 80 130 70 130 50 NS to NS SO Nov 160 170 140 170 170 210 160 160 100 180 160 170 160 170 150 180 210 180 200 110 210 230 i Annuar Menn 227 187.5 276 243 242 205 246 253 211 198 204 195 232 215 203 193 253 220 260 188 274 243 Amwa tug 1) l t Fee < 76 < SO 125 50 141 < 50 60 120 111 70 59 70 33

• 50 59 90 NS 70 117 140 106 100 May

• 2< 50 5= 50 36 < 50 30 50 34 < SO 23 4 50 44 < 50 49

• 50 < 50 < 50 < 50 < $3 0< 50 4 Aug < 50 < 50 110 170 < 50 70 80 140 < 50 50 < 50 50 < 50 210 < 50 60 < 50 170 < 50 80 * $3 250 Nov 50 < 50 150 70 e 50 4 50 90 50 70 < 50 60

• 50 90 60 50 e 50 120 60 < 50 60 80 50 Annual Meen

• 44 5 < SO 97.5 85 69.3 < 55 65 90 66.3 55 46 55 54.3 92.5 52 82.5 73.3 87.5 < 66 8 82 5 59 113 ,"

istai Pnosor*otous (ug1) e Feb 9 10 9 9 8 to 3 8 11 14 5 7 9 7 10 13 NS 13 11 31 15 32 '

J May 9 10 7 11 6 9 8 14 7 7 8 9 13 12 8 13 11 14 13 13 13 11 t L Aug < 5 10 5 8 12 6 5 6 9 7 10 6 8 7 < 5 7 < 5 9 8 13 < 5 11

-J Nov 28 to 11 6 8 to 10 7 5 11 14 9 7 8 9 9 13 10 7 13 17 16 Annuat vean 12 8 10 8 85 8.5 8.75 8 8.75 8 9.75 8.75 7.75 9.25 8,5 8 10.5 9.67 11.5 9 75 17 5 12 5 17.5 Wogees; rate ug1) s Feb 15 < 5 6 to 22 to 8 15 20 8 11 10 13 7 15 6 NS 12 14 to 12 17 May 3 8 5 to 4 14 6 19 3 5 3 11 6 7 6 11 11 9 to 5 = 54 5 Aug < 5< 5 9 to < 5* 5

• 5= 5 5= 5 6* 5 < Se 5 < 5 7 5 5 5 6

• 5 8 ,

Nov 20 < 5 13 10 10 17 38 7 9 8 18

• 5 17 5 5' < 5 8 5 14 11 15 10 Arvua! Mean 10 8 < 5 75 8 25 to 10.3 11.5 14 3 11 5 3.25 6.3 9.5 7.75 10.3 6 7.75 7.25 8 7.75 10.8 8 9 25 to I

SAca (rg1) 5 I Fen 4.8 4 5.1 4 4.9 4 4 4.8 4 4.8 4 4.8 4 5 4 NS 4 4.6 4 5.4 May 4.7 3.7 5 4.2 46 3.6 5.1 5 . 4.2 4.7 3.8 4.7 3.7 5.1 4.3 4.6 3.8 5 4.2 4.5 4 4.5 4.5 f Aug 3.3 3.8 4.7 5 3.4 3.9 4.7 5 3.3 3.8 3.3 3.4 3.8 3.8 3.4 3.8 3.7 5.1 3.4 4.3 3.7 5 l Nov 41 4.1 4.1 4 4.1 39 43 4 4 4.1 4 4 4.2 39 4 4.2 4.7 4 44 41 47 43 Amuel Mean 4 23 39 4 73 43 4 25 3 85 4 78 4.3 4.2 3.93 42 3.88 4.48 4 4.25 3.95 4.47 4.33 4 23 41 4 SS 4.7 t I

NS e Not Sampled  ;

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1. N FEB VAR ' APR MAY JUN 'JUL AUG ' SEP OCT NOV ' OEC Month  :

E 1994 C 1995 Figure 2-2. Monthly precipitation in the vicinity of McGuire Nuclear Station.

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Jan Feb Mar i

Temperature (C) Temperature (C) Temperature (C) 0 5 10 15 20 25 30 35 0 5 10 15 20 25 30 35 0 5 '-10 15 20 25 30'-35

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25- 255 25i 30i 30i ) 30i , J 35- i 35U 35-Figure 2-3. Monthly mean temperature profiles for the McGuire Nuclear Station background zone in 1994 (mm) and 1995 (-).

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O O O Jul Aug gep Temperature (C) Temperature (C) Temperature (C) 0 5 ' 10 15 20 25 30 35 0 5 '1G 15 23 25 '--- 30 '-

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352 35-Figure 2-3. Monthly mean temperature profiles for the McGuire Nuclear Station background zone in 1994 (en) and 1995 (-).

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• Temperature (C) Temperature (C) Temperature (C) 0 5 ' 10 15 ' 20 ' 25 ' 30 '-35 0 5 10 15 20 25 30 35 0 5 10 ' 15 '-20 25 '-30 35 '

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352 35- 352 Apr May Jun

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352 35-t Figure 2-4. Monthly mean temperature profiles for the McGuire Nuclear Station mixing zone in 1994 (me)and 1995 (-).  :

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352 352 352 Oct Nov Dec Temperature (C) Temperature (C) d Temperature (C) 0 .g },0 },5 2,0 2,5 ' 3,0 35 0 y 10 1,5 2,0 _ 25 3,0 35 2 25 30 35 0

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35- , 350 352 Figure 2 4. Monthly mean temperature profiles for the McGuire Nuclear Station mixing zone in 1994 (m) and 1995 (-).

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Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Month ^

Figure 2-5. Monthly temperature and dissolved oxygen data at the discharge location (loc 4.0)in 1994 (m) and 1995 (O).

2-24

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Oct Nov Dec ta t-J Oxygen (mg/L) Oxygen (mg/L} Oxygen (mg/L)

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g20- p g20- g20-25-' ,[ 25i 25i 30H 30i k 30i 352 , 352 352 Figure 2-6. Monthly mean dissolved oxygen profiles for the McGuire Nuclear Station background zone in 1994 ( ) and 1995 (-).

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'.J Apr May Jun to 9

Oxygen (mg/L) Oxygen (mg/L) Oxygen (mg/L) 0 2 4 6 8 10 12 0 2 4 6 8 10 12 Q 2 4 6 8 to 12 0 * ' ' ^'  ;' '

0 ' ' '-

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35- 35- 352 Figure 2-7. Monthly mean dissolved oxygen profiles for the McGuire Nuclear Station mixing zone in 1994 (sm) and 1995 (-).

~

O O O Jul Aug Sep Oxygen (mg/L) Oxygen (mg/L) Owen (mg/L) 0 2 4 6 8 10 12 0 2 4 6 0 10 12 0 2 4 6 8 to 12 "

0 ' ' *-- ' ' '

0 ' '" ' ' ' '

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5- ' 5- ,/ Si 10i 10i

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g20-255 25- 25-30- 30-30- ,

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352 35- 352 Oct Nov Dec (3 Oxygen (mg/L) ,

Oxygen (mg/L) Oxygen (mg/L)

Oc 0 2 4 6 0 10 12 0 2 4 6 9 10 12 0 2 4 6 8 10 12 0, 0, 0' .

l  !

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g 20-1 y 20;

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320- j 25- 25i 255 30- 302 I 30i ,

- - k l }j 352 ,

35- 352 Figure 2-7. hionthly mean dissolved oxygen profiles for the hicGuire . Nuclear Station mixing zone in 1994 (sm) and 1995 (-).

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O Sempting Locatbns O 240 ~

O Sampling Locations 235- 1.0 se 11.o 13 o 15 0 1s e ele es o 710 80 0 235i 1.0 a.o 11.0 13.0 ts.o 1s.e s2.0 es O F1.o so.o a 4 8 4 4 4 4 4 4 4 4 I 4 4 4 4 4 4 8 4 23 5 *A *N 130k jep ags a

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• I l 205i lf rosi = f Temperature (deg C) .

N Temperature (deg C) 200- ,200-Jan 10,1995 .J Feb 7.1995 195~ , ..

.,. .,. .,. .,. .,. ... ... ... , tof" ... .. ..

i. . ,

to 15 20 25 30 35 40 45 50 55 to 15 20 25 30 35 40 45 50 55 .

Distence from Cowens Ford Dem (km) Dierence from Cowens Ford Dem (km) iJ gg 240 24C

• Sampang Locations Sampang Locatione 235{ io ao ti o 130 1so 1se e2 o es o 72 0 ao.o 23k 1.0 so tis

• 13 e 1so iae sto . es o 72 0 so c e a 4 4 4 4 4 4 4 & & 4 4 4 4 4 4 4 4 4 22

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210- 210-o 205i 205' Temperature (deg C) .

Temperature (deg C) 200- 2CO.

Mar 7,1995 Apr 4.1995 195' , ... ... ... ... ... .,. .. . .

... ., 16 , . . .,. ... ... . . ... ,,. ... , .,

DIstence from Cowene Ford Dem (km) Olstance kom Cowens Ford Dem (km)

Figure 2-8. Monthly reservoir-wide temperature isotherms for Lake Norman in 1995.

av 24C Sampling Locations SampEng Locations 23N to eo 11 0 13 0 is o 15 e e20 es 0 72 o 80 c 23 1.0 eo 11 0 110 15 0 1s a e20 es a 720 es o a 4 4 4 1 4 4 4 8 4 4 4 4 4 4 4 4 4 4 &

23 64 / ) V Z' 20/ @ O 236 M 20 '

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N May 8,1995 Jun 8,1995 195 .,. .,. .,. .,. .,. .,. .,. .,. .,. .,. ., 195~ .

0 5 to 15 20 25 30 35 40 45 50 55 0 5 15 20 to 25 30 35 40 45 50 55

• Distance from Cowans Ford Dam (krn) Distance from Cowans Ford Dam (km) 1J

.L 24C 24C O Samphng Locations Sampling Locations 2354io ao 11 o 13 o is o 15 a e20 es o 72 0 83 0 23k 1.0 e.0 11.0 13 0 1$ 0 15.0 a

elo es o 72 0 to o a 4 4 4 4 4 4 4 4 4 4 4 4 4 4 & 6 4 4 ass a '" 26 e 23> 9

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20 s , Temperature (deg C) 20g Temperature (deg C) 1 4 Jul 7,1995 . Aug 9,1995 195,. ..

,. .,. ,. .,_ ,. .,. ... ,. ., ., 195 ,,. ... ...

0 5 10 15 20 25 30 35 40 45 50 55 0.

5 to 15 20 25 30 35 40 45 50 55 Omtance from Cowens Ford Dam (km)

Distance from Cowans Ford Dam (km)

Figure 2-8. Continued.

/~~%*

• 24

, J 240 -"

Sampling Locat!ons Sampfing Locations, 235i io a0 11.0 13 0 15 0 15.9 62.0 63 0 72 0 80 0 s a a a a a 6 a 23k 1A 8.0 11.0 13.0 15 0 15 9 620 69 0 72 0 53 0 a 4 & a a a a a

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i 16s Temperature (deg C)

gl 20g Temperature (deg C)

/ Sep 13,1995 195 Oct 12,1995

... . 195' . . . . . . . . . . .

Distance from Cowans Ford Dam (km)

Distance from Cowans Ford Dam (km) iJ 240 240 h Samphng Locations Sampfing Locations 235)io eo 11 0 13 0 15 o ts.e e2 o es.o 72.0 a0.0 4& 6 1 4 4 & 4 & 4 4 23k 1.0 s0 11.0 13 0 15 0 15.e e2 0 se o 72 0 e3 0 4 4 4 4 & 4 4 4 4 4 &

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Distance from Cowans Ford Dam (km)

Distance from Cowans Ford Dam (km)

Figure 2-8. Continued.

~

O 2kb, O 24C 0 ,

Sampling Locations Sempting Locations i 235{ to so 11 0 13.0 15 0 15.s e2 0 es o 72 0 s3.0 23 S t.o a.o 11.0 13.0 1s.0 t s.e e2.0 es o 72 0 40.0 3 8 4 4 4 8 4 4 4 8 4 4 8 8 8 4 e a 8 a 4 230; -

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205-' 205' DisscNed Oxygen (mg5) ,

DissoNed Oxygen (mg1) 200- 200-Jan 10,1995 Feb 7,1995 195 , ... .,, ... ... .,, .,. ... . .

... ,, 100' , ... ... .,. .,. .. .. ... .,. .,. . ,

10 15 20 25 30 35 40 45 50 SS to 15 20 25 30 35 40 45 50 55 Distance from Cowens Ford Dam (km) Distence from Cowens Ford Dem (km) e 240 24C' Sampling Locations Sampling Locatione

~

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, Dissoked Oxygen (mg5) .

DissoNed Oxygen (mgi) 200- 200- -

Mar 7,1995 Apr 4,1996 195 f

... ... ... . . ... . . ., 1..~ ... ... ... ... ... . . ... ... ... .. . ,

Distance from Ccwans Ford Dem (km) Distance from Cowens Ford Dem (km)

Figure 2-9. Monthly reservoir-wide dissolved oxygen isopleths for Lake Norman in 1995.

_ _ _ _ _ _ . . _ __ . _ = _ , . _ . . . .. _ - _ _ _ . ,

n -

, n v 24c h Sampung Locations Sampling Locations 235 10 80 11 0 13 0 15 0 15 9 62 0 59 0 72 0 80 0 23 1.0 80 11 0 13 0 110 16 9 62 0 69 0 72 0 83 0 i

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" 210-8 210-1 205 205' 200: O Dissolved Oxygen (mg/l) 20s } Dissolved Oxygen (mgM)

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• 35 .,50 55 Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dant (km) o iJ EJ 240 240- -

N Sampling Locations

. Sampling Locations 23% 10 00 11 0 13 0 15.0 15 e

. a a a e2 0 e9 0 72.0 e0.0 23k 1.0 e.0 11.0 13 0 1s.0 15.9 e2.0 es 0 72 0 so 0 4 4 & 4 a a 6 4 4 4 4 & 4 a 4 4 23  % i d 8 22 % A 3

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Dissolved oxygen (myl)

• 24 b 1 Jul 7,1995 Aug 9,1995 195 . .,. .,. .,. .,. .,. .,. .,. .,. ,. .,. ., 195^ .

0 5 10 15 20 25 30 35 40 45 50 55 0 5 to 15 20 25 30 35 40 45,. 50 .,55 Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)

Figure 2-9. Continued.

240 240 Sampling Locations ,

S&mpung Locations-235' i0 80 11 0 13 0 15.0 15,s e2.0 es c 72 0 so.c 23k t .0 s.0 11.0 13.0 15.0 15.s - 62.0 st o 72 0 e00  !

. 4 , . a . , , a a . . a . . a . . a s.

5 220' 220' i ') *A g ,

5 215: 2152 a ' .vp 5 @ . N -

5 2 .,

2co: Dissdved Oxygen (mg/l) 20c Dissdved Oxygen (mg/l) l Sep 13,1995 J Oct 12,1995 -

195 . . . . . . . . . . . . . . . . . . ., 1P5 . . . . . . . . . . . . . . . . .

Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)  ;

',' 240 b

?

$ 2tc) . Sampting Locations Samp5ng Locations 235 to 80 11 0 13 0 15 0 15.s 62 0 69.0 72.0 80 0 23k t.0 8.0 11.0 , 13 0 15.0 159 610 69 0 72 0 e30

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Dissdved Oxygen (ny/l) 23g Dissdved Oxygen (mg/l) l Nov 20,1995 T Dec22,1995 195 . . ... . . . . . . . . .,. ... . . .

195 . . . . . . . . .

Distance from Cowans Ford Dam (km) Distance from Cowans Ford Dam (km)

Figure 2-9. Continped.  :

+

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95010 95066 95124 95159 95188 95221 95256 95324 Julian Date Figure 2-10a. Heat content ofthe en. ire water column (E) and the hypolimnion (0)in Lake Norman in 1995.

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O 2-35

C O

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Figure 2-11. Continued.

u l

1 l

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Cll APTEll 3 i

PIIYTOPLANKTON j INTRODilCTION j Phytoplankton population parameters were monitored in 1995 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, l August, November 1995) with historical data collected during these same  :

I months.

O  !

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; llodriguez 1982). Rodriguez (1982) classified the lake as oligo mesotrophic based on phytoplankton abundance, distribution, and taxonomic composition.

METHODS AND MATEltlALS Quarterly sampling was conducted at Locations 2.0, 5.0, 8.0, 9.5, i 1.0,13.0,15.9, and 69.0 in Lake Norman (see map oflocations in Chapter 2, Figure 2-1). Duplicate composite grabs (

from 0.3,4.0, and 8.0 m (i.e., the euphotic zone) were taken at all locations. Sampling was - i

\

conducted on 24 February, 31 May, 30 August, and 1 November 1995. Phytoplankton density, biovolume and taxonomic composition were determined Ibr 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 fbr samples from all locations. Chlorophyll a and total phytoplankton densities and biovolumes are used in determining phytoplankton standing

{}

crop. Field sampling methods, and laboratory methods used Ihr chlorophyll a, seston dry 3-1

O weiahts med nogeietion identificetien end enemeretien were identicei te the e e ed by Rodriguez (1982). Data collected in 1995 were compared with corresponding data from quarterly monitoring beginning in August 1987.

A one way ANOVA was performed on chlorophyll a concentrations, phytoplankton densities and seston dry and ash free dry weights by quarter. This was followed by a Duncan's Multiple Range Test to determine which location means were significantly different.

RESULTS AND DISCUSSION Standing Crop 4

Chlorophyll a Chlorophyll a concentrations ranged from a low of 2.15 mg/m3 at Location 69.0 in November to a high of 12.45 mg/m3 at Location 15.9 during the same month (Table 3-1.

Figure 3-1). All values were well below the North Carolina water quality standard of 40 h mg/m3(NCDEHNR 1991). The range of chlorophyll observed in 1995 was similar to those observed during previous years since 1987, and Lake Norman continues to be in the mesotrophic range.

During 1995, the clear trend of increasing chlorophyll a concentrations from downlake to uplake was not as apparent as in 1994 (Duke Power Company 1995). Locations 15.9 (uplake, above Plant Marshall) and 69.0 (uppermost, riverine location) had significantly higher values than downlake, Mixing Zone locations (2.0 and 5.0) on only two occasions, and during February, Locations 5.0 and 9.5 had significantly higher concentrations than 15.9 and 69.0 (Table 3-2). Chlorophyll concentrations at Location 69.0 varied considerably with maximum lakewide gnarterly values occurring on May and August, and minimum values observed in February and November. The riverine zone of a reservoir is subject to wide fluctuations in flow depending, ultimately, on meteorological conditions (Thornton 1992), although .

influences may be moderated due to upstream dams. During periods of high flow, algal production and standing crop would be depressed due in great part to washout. Conversely, production and standing crop would increase during periods of low flow and high retention time. Chlorophyll a concentrations at Location 2.0 the most downlake location, were within O

l 3-2 I

1

- __ .. . - - - - - - - ~ - .- - - . -. .- -. -

O the seme reese e Locatiee 5.0. the other Mixinszeee iecetien. in Mer eed Nevember. bet had significantly lower chlorophyll concentrations in February and August.

i i

Chlorophyll a lakewide annual means by quarter ranged from approximately 4 to 8 mg/m3 in 1995, and were within ranges of lake means observed since 1987 (Figure 3-2). A trend of

increasing values through the year, from February through November, was observed among lake means. The mean for November was nearly twice that of February, and maximum yearly chlorophyll concentrations were observed at all but Location 69.0 that month.

Average annual chlorophyll concentrations during the period of record were highest in 1991 and 1992, then generally decreased through 1994-1995 (Figures 3-2 and 3-3). Notable

. exceptions were Locations 5.0 and 9.5 which showed gradual increases for each November through 1995.

Total Abundance Phytoplankton abundance, represented by total densities and biovolumes, was lowest in O February, and highest in May (Table 3-3, Figure 3-1), as was the case in 1994 (Duke Power Company 1995). The minimum density and biovolume observed in 1995 occurred at j Location 15.9 in February (1033 units /ml and 503 mm3/m 3 , respectively) and the maximum was found ai Location 11.0 in May (5354 units /mi and 3562 mm3/m3 , respectively). These maximum values were still below the NC state standard definition for phytoplankton blooms of greater 10,000 units /ml and 5,000 mm 3 /m 3 (NCDEHNR 1991). Total densities in the Mixing Zone (2.0 and 5.0) were not significantly different during May through November; while in February, Location 5.0 had a significantly higher density than Location 2.0 (Table 3-i 4). During August and November, Location 15.9 had significantly higher densities than all other locations. During May, Location i1.0's density was significantly higher than other locations. The general trend of increasing densities from downlake to uplake observed in 1994 was not as apparent in 1995, and did not follow long term trends of mereasmg nutnent concentrations from downlake to uplake locations (Duke Power Company 1995). .

Seston Seston dry weights represent a combination of algal matter, other organic material, and inorganic components. Seston dry weights were significantly higher at Location 69.0 than at 3-3

1 l

O ether iocetiem in Mex eed ^use i; whiie in Febreery eed sevember, dry weishte were in the  !

mid range (Table 3-5). Again, this shows a change from the previously reported pattern of

increasing values from downlake to uplake observed in 1994 (Duke Power Company 1995). I 3

Also, during 1995, seston dry weights did not show as much spatial or temporal variability as

- in the previous year. Mean values ranged from 2.65 mg/l at Location 2.0 in August to 7.46 )

mg/l at Location 15.9 in February (Table 3-5, Figure 3-1), compared to a range of 1.25 mg/l i to over 20 mg/l during 1994 (Duke Power Company 1995). This would indicate less variability in inputs prior to sampling time, and more consistent conditions from Location 15.9 to the forebay in 1995 than occurred in 1994.

i i Seston ash free dry weights represent organic material, and should be more closely related to 4

, algal standing crop parameters. For the most part this was the case, with maximum values occurring at Locations 15.9 and 69.0 during all quarters (Table 3-5). In terms of statistical

significance, patterns were less well defined, and Location 69.0 had a significantly higher

,f values only in May. Ash free dry weights ranged from 0.99 mg/l at Location 8.0 in l November to 4.57 mg/l at Location 15.9 in February, which was similar to the range

observed in 1994 (Duke Power Company 1995). Lower lake locations tended to have higher a

O t tal and ash free dry weights than in 1994. The proportions of ash free to total dry weights in 1995, as compared to 1994, indicated proportionally higher amounts of organic materials into l I

the lake.

1 l i

+

Secchi Depths Secchi depth is a measure of light penetration. Secchi depths were often the inverse of

) suspended sediment (seston dry weight), with the lowest depths at Locations 11.0 through 69.0 and highest from Locations 9.5 through 2.0 downlake. Depths ranged from 0.45 m at Location 13.0 in February to 2.45 m at Location 9.5 in August (Table 3-1).

1 i

Community Composition l

Ten classes comprising 73 genera and 120 taxa of phytoplankton were identified in plankton samples during 1995. The distribution of taxa within classes was as follows: Chlorophyceae (green algae), 53; Bacillariophyceae (diatoms), 27; Chrysophycaea,15; Haptophyceae and Xanthophyceae, one each: Cryptophyceae (cryptophytes), 4; Myxophyceae (blue-green Q algae) 10; Euglenophyceae (euglenoids),3; Dinophyceae (dinollagellates) 5; and one taxon 4

3-4

f .a the Chloromonadophyceae. Since the study began in 1987, over 100 genera and more than 260 taxa have been recorded. No new taxa were observed in 1995.

Species Compositon and Seasonal Succession t

Lake Norman supports a rich community of phytoplankton species. This community varies l both seasonally and spatially within the reservoir. In addition, variation is also often found between years for the same months sampled. As mentioned earlier, no bloom conditions were observed during 1995 sampling periods, and no substantial numbers of nuisance algae were found. ,

Cryptophytes generally dominated algal densities in February due to the abundance of Rhodomonas mimita, which comprised over 40 % of the density at most Locations that month (Figure 3-4). This was similar to results from 1994. Rhodomonas mimita has been the most frequent numerical dominant observed in the lake (Duke Power Company 1995).

Cryptophytes also dominated biovolumes at Locations 5.0,9.5, and i1.0; while diatoms had the highest biovolumes at Locations 2.0 and 15.9. due to the abundance of the large centrate, O ^ <ciosire a m hix " a. ^ <eio sira a m aix ~ a isi iv P cativ e b u e a ent d erin a ih e e netretirie d n erio d ie Lake Norman, often reaching peak abundances in late winter and early spring. The population density declines at the onset of stratification, as this species forms a resting stage which settles to the bottom sediments (Buetow 1988).

1 Phytoplankton abundance increased substantially in May, and both densities and biovolumes were dominated by diatoms which constituted over 70 % of the density and biovolume at all locations (Figure 3-4). The most abundant species was the pennate Fragitaria crotonensis.

This species generally contributed 50 % or more to densities, and dominated all biovolumes at Lake Norman locations. Rhodomonas mimaa was ranked second in density at all locations, but never constituted more than 15 % of any total density. This represents a shift from May 1994 when Rhodomonas mimaa was the principal numerical dominant (Duke Power Company 1995). .

As in past years the phytoplankton community in August consisted of a diverse assemblage dominated by green algae at Locations 2.0, 5.0, and 9.5. Diatoms were most abundant at locations 11.0 and 15.9 (Figure 3-4). The most important green alga during August was the 0 small desmid Cosmarimn asphearosporum var. strigosmn, a common constituent of Duke 3-5

\

O Pewerre ervoir during midteiete um mer. otherimnertentcon titueet were onidentitied coccoid green algae. Dinoflagellates generally dominated biovolumes due primarily to their large individual biovolumes, since they seldom exceeded 8 % of the densities. In terms of biovolume, the large dinoflagellate, Peridinimn wisconsinense was dominant at all but Location 2.0 in August. While never dominant, blue green algae were more abundant during August than in other months, especially at Location 15.9, where they constituted greater than 17 % of the total density in August. Typically, the highest numbers of blue green algae observed over the course of the Maintenance Monitoring Study were found at Location 15.9 in August (Duke Power Company 1988,1989,1990,1991,1992,1993,1994, and 1995).

Diatoms clearly dominated phytoplankton assemblages during November, often comprising half or more of the density and 70 % or more of the biovolume (Figure 3-4). Most planktonic diatoms are generally adapted to growth at relatively low temperatures and light conditions l

which would explain their abundance during November (Patrick et. al 1969). The i cryptophyte, Rhodomonas minuta was marginally dominant, based on density, in the Mixing Zone. The diatoms Melosira ambigua, M. granulata var. angustissima, and Tabellaria l' fhnestrata were the most abundant forms at Locations 9.5. I1.0, and 15.9, respectively.

O r"nezi"ri" ze"e><r"<" domi"eted the aioveieme et eii 8"t 'oceti"" 9.s. where ueze><r" ambigua was dominant. During November 1994, Melosira enbigua was a more important J

constituent of the phytoplankton community, based on biovolumes, than it was in 1995 l (Duke Power Company 1495).

FUTURE STUDIES No changes are planned for the phytoplankton portion of the Lake Norman Maintenance Monitoring program during 1996.

SUMMARY

Chlorophyll a concentrations at all locations during 1995 were within ranges reported during -

previous years, and Lake Norman continues to be classified as mesotrophic. The maximum chlorophyll value of 12.4 mg/m 3was well below the NC State Water Quality standard of 40 mg/m3. Lakewide chlorophyll means increased from February through November. During 1995, the trend ofincreasing chlorophyll concentrations from downlake to uplake was not as b

v 3-6

O engerent as ie i994. tecetiee 69.0. the me i riverine iocetion. howed e wide reece of variability as compaied to 1994.

Seston dry weights were not as variable spatially and temporally in 1995 as in 1994; the trend of increasing values downlake to uptake was not as apparent in 1995 as in previous years.

This indicates that more stable conditions existed prior to sampling times during 1995.

Based on proportions of ash free (organic) dry weight to dry weight, higher amounts of organic material were present in 1995 than in 1994.

Total phytoplankton densities and biovolumes observed in 1995 were within the range of those observed in previous years. Based on NCDEHNR (1991), the maximum density and

. biovolume were below state standards of 10,000 units /ml and 5,000 mm3/m3 and no bloom conditions were recorded at times of sampling. Densities and biovolumes were lowest in j February and highest in May, as was the case in 1994. Again, the previous year's trend of increasing values downlake to uplake was not as apparent in 1995, indicating a change in spatial variability.

l O Overall phytoplankton c mmunity c mp sition was generally similar to that of the previous year, with typical seasonal and spatial variability. Cryptophytes, diatoms, and green algae were the most abundant forms in 1995. Cryptophytes generally dominated phytoplankton communities in February, while diatoms were most abundant in May and November.

Community composition in November 1994 compared with November 1995 showed a shift from cryptophytes to diatoms. Green algae most often dominated densities downlake in August; while diatoms were most abundant uptake. Dinollagellates, due to their large individual sizes, dominated biovolumes at all locations in August. Although blue-green algae were more important in August than in other months, they were never the dominant component at any location at any time in 1995.

Major taxa observed in 1995 were generally similar to those observed in 1994. Rhodomonas minuta was the most frequent numerical dominant during 1995 as in previous years. -

Melosira ambigua, while an important component of biovolumes in 1995, was not dominant as often as in 1994. Another diatom, Fragilaria crotonensis, dominated algal biovolumes in May.

O 3-7

i O LirEitaruRE CirED Buctow, D. H.1988. A Characterization of the Freshwater Diatom, Melosira italica, Collected from Lake Norman, NC. MS Thesis U.N.C.C.155 pp.

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.1988. Lake Norman maintenance monitoring program:  ;

1987 summary. I Duke Power Company.1989. Lake Norman maintenance monitoring program:

1988 summary.

Duke Power Company.1990. Lake Norman maintenance monitoring program:

1989 summary.

O Duke Power Comenny.1991. Lake Norman mainteeance monitoring vrearem:

1990 summary.

1 Duke Power Company.1992. Lake Norman maintenance monitoring program:

1991 summary.

Duke Power Company.1993. Lake Norman maintenance monitoring program:

1992 summary.

)

Duke Power Company.1994. Lake Norman maintenance monitoring program:

1993 summary.

Duke Power Company.1995. Lake Norman maintenance monitoring program:

1994 summary.

Menhinick, E. F. and L. D. Jensen.1974. Plankton populations, p. 129-138 In -

L. D. Jensen (ed.). Environmental responses to thermal discharges from Marshall Steam Station, Lake Norman, NC. Electric Power Research Institute, Cooling Water Discharge Project (HP-49) Report No.11. Johns l Hopkins Univ., Baltimore MD. 235 p.

O-3-8

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

O N rth Carolina Department of Environment, Health and Natural Resources, Division of Environmental Management (DEM), Water Quality Section.

1991.1990 Algal Bloom Report. i Patrick, R., B. Crum, and J. Coles.1909. Temperature and manganese as determining factors in the presence of diatoms or blue green algal flora in ,

streams. Proc. Acad. Nat. Sci. Philadelphia, 64:472 478.  !

. Rodriguez, M. S.1982. Phytoplankton, p. 154-200 In J. E. Hogan and W. D.  ;

Adair (eds.). Lake Norman summary, Technical Report DUKEPWR/82-02 Duke Power Company, Charlotte, NC. 400 p. .

1 Thornton, K. W., B. L. Kimmel, F. E. Payne.1990. Reservoir Limnology. John Wiley and Sons, Inc. N. Y. 24G pp. i O ,

i O  !

3-9

l O Tenie 3-1. uee chiernhvit e coece tretieme <mulm >e ie comve8ite e mvies co.3 4, and 8m depth) and secchi depths (m) observed in Lake Norman, NC, in 1995.

Chlorophyll a l

Location FEB MAY AUG NOV 2.0 3.44 5.32 3.86 6.98 ,

5.0 5.71 4.89 5.01 6.25 l 8.0 4.30 6.07 6.48 7.42 9.5 5.74 5.76 7.93 8.12 l 11.0 4.42 5.83 5.32 11.46 j 13.0 3.41 5.98 2.70 8.23 l 15.9 3.45 6.16 8.12 12.45 l 69.0 2.99 7.06 8.50 2.15 l Secchi depths Location FEB MAY AUG NOV 2- '4 23 '7 O' 5.0 1.20 2.10 1.70 1.75 8.0 1.30 2.30 1.90 1.70 9.5 1.20 2.30 2.45 1.80 11.0 0.65 2.10 1.85 1.60 13.0 0.45 1.80 1.25 1.40 15.9 0.70 1.80 1.70 1.50 69.0 1.00 1.25 1.30 1.55 l

I l

i O

3-10

.i 4

i

{

3 O Table 3 2. Duncan's Multiple Range Test on chlorophyll a concentrations in Lake Norman, NC, during 1995.

i )'

l 1

1 4

i ,

j' February Location 69.0 13.0 2.0 15.9 8.0 11.0 5.0 9.5'  !

l Mean 2.99 3.41 3.44 3.45 4.30 4.42 5.71 5.74 r

, I j

May Location 5.0 2.0 9.5 11.0 13.0 8.0 15.9 69.0 1 . Mean 4.89 5.32 5.7G 5.83 5.98 G.07 G.16 7.06  ;

j .

l 1 1 I

1 l August Location 13.0 2.0 5.0 11.0 8.0 9.5 15.9 69.0 i Mean 2.70 3.8G 5.01 5.32 6.48 7.93 8.12 8.50  :

l l

i i O- November Location 69.0 5.0 2.0 8.0 9.5 13.0 11.0 15.9 1

Mean 2.15 0.25 6.98 7.42 8.12 9.23 11.46 12.45 I

i 1 l t

! 1 i

3 i

l

!O -

.k 3-11 i

)

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

I, l

l O Table 3 3. Total mean phytoplankton densities and biovolumes from samples collected in Lake Norman, NC,in February, May, August and November 1995.

Total Phytoplankton - Lake Norman - 1995 l

! Density (No./mi)

Locations  !

2.0 5.0 9.5 11.0 15.9 Mean FEB- 1038 1906 1786 1202 1033 1393 MAY 2638 2169 3584 5354 3737 3496 AUG 1317 1622 1574 1382 3671 1913 NOV 1677 1562 1885 2000 4288 2282 -

3 Biovolume (mm /m )

Locations l 2.0 5.0 9.5 11.0 15.9 Mean '

FEB 637 815 978 554 503 697 MAY 1962 1677 3056 3562 3096 2670 ,

AUG 1175 1435 2406 1202 1791 1602 NOV 990 897 1358 1295 2649 1438 O ,

m O

3-12

O Tenie 3-4 o""c"='e " "itivie ae"ne Testoe v xtevieektee Norman, NC, during 1995.

n aemeitiesim teke February Location 15.9 2.0 11.0 9.5 5.0 Means 1033 1164 1202 1786 190G May Location 5.0 2.0 9.5 15.9 11.0

, Means 2169 2G38 3590 3737 5354 August Location 2.0 11.0 9.5 5.0 15.9 Means 1317 1382 1574 1G22 3G71 1

November Location 5.0 2.0 9.5 11.0 15.0 Means 15G2 1G77 1885 2000 4288 9

O 3-13

l O Tante a-5. o mee uuiti ie 9 no#ee Teet ee eeeteu arv aua een tree arr -eie (g/m3) in Lake Norman, NC, during 1995.

nt DRY WelGHT February Location 8.0 9.5 5.0 2.0 69.0 11.0 13.0 15.9 Mean 3.50 3.58 3.83 3.90 4.73 5.79 7.24 7.46 May Location 9.5 8.0 5.0 11.0 2.0 13.0 15.9 69.0 l Mean 3.15 3.23 3.43 3.53 3.73 3.83 4.16 7.17 l

August Location 2.0 11.0 13.0 15.9 5.0 9.5 8.0 69.0 Mean 2.65 2.68 2.99 3.04 3.16 3.28 3.39 G.58  !

November Location 8.0 2.0 9.5 69.0 11.0 5.0 13.0 15.9  !

Mean 3.82 3.85 3.93 3.98 4.17 4.28 4.40 4.57 j I

O ass esee Dav weiGs1 February Location 69.0 8.0 9.5 5.0 2.0 11.0 13.0 15.9 Mean 3.82 3.85 3.93 3.98 4.17 4.28 4.40 4.57 May Location 5.0 9.5 11.0 2.0 8.0 13.0 15.9 69.0 Mean 1.29 1.38 1.42 1.42 1.44 1.47 1.67 2.22 August Location 2.0 13.0 11.0 5.0 15.9 9.5 8.0 69.0 Mean 1.09 1.21 1.37 1.45 1.G3 1.88 2.08 2.23 November Location 8.0 13.0 9.5 69.0 5.0 2.0 11.0 15.9 Mean 0.99 1.12 1.13 1.14 1.1G 1.19 1.33 1.38 O

3-14

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

l O CHLOROPHYLL a (mg/m3) l DENSITY (units /ml) 14 6000 12 .- .- -..-. . .._- --.

l -.__ ___..--_... - ....

I i

10 -..__ ..._. --- _. ...

l 4000 ._.._____..._._.._____

l 8 -. . .... ___. _) I

)

, ) i 3000 .......__ .__ ._____ _ . .

[

6 l i

2000 __-.. __ . e.

4 ..._ ...___.

j j , , i

, 1 2 -.___. . _-..---...--_ _: 1000< -- --__.__.... ___.... >

0 0 20 50 80 9.5 11.0 13 0 15 9 69 0 2.0 5.0 95 11.0 15.9 q

SESTON ORY WElGHT (mg/l) l I e ll i 4000 BIOVOLUME (mm3/m3) l 7 _ .-..__. _. .. _ -. ..

I 3500. .. ____ ...__ __

I l

l 8 . _ . .... . ._._

3000 -.. ... ... .-.. _. . _.'

5 ,<

l .. _-._. _ . . _ _ _ - .

2500 -. ....__.. .. ....._ .

j 4 -t l 2000, - --- . ._- _._.. . _

t l > <

3 ... - . .

1500 ...... . .. _ __

2 -- - -

t 1000) _. ___........ l i 1 --- - --- ----

l I 500 ' -__. .---._. __ .

i  !

0 o

$ n . $ -

20 5.0 9.5 11 0 15 9 LOCATIONS LOCATIONS FEB MAY AUG NOV

-+- - m - -o - -x- .

Figure 3-1. Phytoplankton chlorophyll a, densities, and biovolumes; and seston dry weights at locations in Lake Norman, NC, in February, May, August, and l November 1995.

l O

l 3-15 1

pr Q ,7 12 . _ _

10

.~

N 0 ) l R I E

I 6 ,

. [ # 1 O I m

z _,  !

o 4< 3 l

/ l 2

l

/ T l N. ! l l

i 0i _ . _ _ _ _ _ _

l FEB MAY AUG NOV MONTH

-+ 1987 -.-e 1988

• 1989 -m- 1990 w 1991 l

- 1992 1993 . e 1994 -e- 1995 Figure 3-2. l'hytoplankton chlorophyll a annual lake means from all locations in Lake Norman, NC, for each (luarter since August 1987.

l l

• /

1 3-16

i l

l l

r CHLOROPHYLL a (mg/m3) l i

FEBRUARY MAY

+ 20 -e 50i --+- 2 0 --o- 5 0

'iliilND~205 $ MIAINT to 10 ZONE 8 , 8 _

6 6 _

4 4 2 2 ,

0 0 87 88 89 90 91 92 93 94 95 81 88 89 90 91 92 93 94 95 I-+ 8 0 -e 95; --o- 8 0 -e- 9 51 12 12 10 10 8 8 _ _

6 6 '

g 4 >

4 2

, l 0 0 _ _ _ _ _ _ l 87 88 89 90 91 92 93 94 95 e7 88 89 CO 91 92 93 94 95

--+-- 11 0 4 130s , + 110 4 13 0 } I 12 ,2 10 IC 8 p ,

A '

2 1 2

0 -

C -

87 88 83 90 91 92 93 94 95 8? 88 89 90 91 92 93 94 95

+ 15 9 ' -e 69 0 . -+-.15 9 --o 690 16 16 14 14 12 12 10 10 8 8 2

0 N -

2 0

g- /

87 88 89 90 91 92 93 94 95 87 88 89 90 91 92 93 94 95 .

^

YEARS YEARS Figure 3-3. Phytoplankton chlorophyll a concentrations by location for samples collected in Lake Norman, NC, from August 1987 through November 1995.

O 3-17

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

l CHLOROPHYLL a (mg/m3)

AUGUST NOVEMBER e 2 0 -e 5 0 , +20+50l 10 10 MIXING 20NE MIXING ZONE 8 8 6 6 -  !

4g  ; 4 __~.___ --.

i i

! 2 2l 0 0 l

67 98 89 90 91 92 93 94 95 87 88 89 90 91 92 93 94 95 i + 8 0 -e _9 5 ' . -+- 8 0 95; 14 14 12 12 - --

• 10 10 -

8 8 -

l 6 >

6 -- --

4 F  ; _

4 - ----- - -- -

2 2 0 0 97 80 89 90 91 $2 C3 94 95 87 68 89 90 91 92 93 94 95

_.e_110 + 13 0 + 110 + 3 0 g ,4

_ _ _ _ . _ _ _ _ - _ _ _ _ _ _ _ _ _ , 4., _ _ _ _ - _

e f 8

/-

lVVD:

0 67 88 89 90 91 92 93 94 95 0

87 88 89 90 91 92 93 94 95

+ 15 9 _e 69 0 --+- 15 9 + 69 0 25 .- - 2b 20 20 15 15 10

,i

f. -

': a 0

m 0

87 88 89 90 91 92 93 94 95 67 88 89 90 91 92 93 94 95 YEARS YEARS -

Figure 3-3. (continued).

! O l

3-18

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

a 1

f

~

i DENSITY: unitshnl BIOVOLUME: mm'hn' 6

4 Loc an a sa toc as s sa f

gge , . - . . - - . . . . _ _ _ ~ _ . - . . _ _ . . ,3g . _ . _ . _ . . _.. . . . _ _ ,_

SrJA -.

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m- , . .

ym. .. .

mgues _

- M $$,h -

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O ,

MAY tov F t,8 MAy AUG tov i FLB AUG L LM.: 5.$ g oc,,3 e age . .

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gm. .. . .

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• 3100 +- -

4 Zu- -_ - - - +

f sum . - = ... -~

< O'- -'

O-FEE 4 MAY A#, NOV ggg ygy gn my i 4 0C sta 100, it s g.yg . .

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) -

5m g

i 3

• mal om.s - - - - - -

4 tar g .- . . .

M. , .

g .

- 0 1 FEB MAY Alf, POV FEB MAY AUG f(IV

-l LDG159 IOC 15 9 q,sn . - ~ - ~ gge . . _. ~ . . . . _ . . .. ..

f j ,, .

m 4

! scuo . p==q -

1 I

54l M k=ix Q.

M 'i 5%. . .

m.

ww

! ;w '

if"" . 82  !

i .m . p

- i l**-

e1 a

4

...- a "i -

...J h

gm. . . . . . .

O _ . - ,1 ne uAY MoNms Am mv rre uxY , , , , , , , auc, wav

! cnoRorwccat  :: '.w BAcLLAPIOFtfrCEAE d Illi ll hCHRYSOf+fYCEAE O CT((PTC(wCEAE

..ma w w wcEAc . OtmtfCE AE OTHERS i  !

j Figure 3 4. Class composition of phytoplankton from euphotic zone samples  !~

collected at locations in Lake Norman, NC, during 1995.

4 i

l '

. i 4

a

3-19 i

i

(

l}

V CII APTElt 4 ZOOPLANKTON INTitODUCTION Coeplankton populations were monitored in 1995 in accordance with the NPDES permit for McGuire Niclear Station. The objectives of the Lake Norman Maintenance Monitoring Program for zooplankton are to:

1

1. Describe and characterize quarterly patterns of zooplankton standing crops at selected l locations on lake Norman; and

2. compare and evaluate zooplankton data collected during this study (February, May, August, and November 1995) with historical data collected during the period 1987-1994.

l l

A)

( Previous stu(iies of Lake Norman zooplankton populations have demonstrated a bimodal seasonal distribution with highest values generally occurring in the spring, and a less pronounced fall peak. Considerable spatial and year to year variability has been observed in zooplankton abundance in Lake Norman (Duke power Company 1976,1985; Hamme 1982; 1

Menhinick and Jensen 1974). i h1ETilODS AND MATERIALS Duplicate 10 m to surface and bottom to surface net tows were taken at Locations 2.0,5.0, ,

9.5,11.0, and 15.9 in Lake Norman (Chapter 2. Figure 2-1) on February 27, May 31 August 30, and November 30. 1995. For discussion purposes the 10 m to surflice tow samples are called epilimnetic samples and the bottom to surflice net tow samples are called whole column samples. l.ocations 2.0 and 5.0 are defined as the Mixing Zone and Locations 4-1

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

J 1

Q 9.5, i1.0 and 15.9 are defined as Background locations. Field and laboratory methods for zooplankton standing crop analysis were the same as those reported in Hamme (1982).

, Zooplankton standing crop data from 1995 were compared with corresponding data from quarterly monitoring begun in August 1987.

i A one way ANOVA was performed on epilimnetic total zooplankton densities by quarter.

This was followed by a Duncan's Multiple Range Test to determine which location means i were significantly different.

1 i RESULTS AND DISClJSSION j Total Abundance i

O During 1995, total zooplankton densities in both epilimnetic and whole column samples were most often highest in May and lowest in August (Table 4-1, Figure 4-1). Spring peaks 5

among zooplankton assemblages are typical of Lake Norman (llamme 1982). Epilimnetic

densities ranged from a low of 22,000/m3 at Location 15.9 in February to a high of 1

3 l 254,600/m at this same location in May, this being the highest zooplar.kton density recorded

, smee May of 1988. Whole column densities ranged from 21,400/m3 at Location 2.0 in August to 240,800/m3 at Location 15.9 in May.

Total zooplankton densities were generally greater in epilimnetic samples than in whole -

column samples in 1995, as in previous years (Duke Power Company 1990, 1991, 1992, 1993,1994, and 1995). This is related to the ability of zooplankton to orient vertically in the water column in response to physical and chemical gradients and the distribution of food O

4-2

1 I

i sources, primarily phytoplankton, which are generally most abundant in the cuphotic zone  !

(Ilutchinson 1967).

The general trend of increasing epilimnetic zooplankton population densities from Mixing l Zone to Background locations was observed from May through November (Table 4-2).

Significantly higher standing crops were observed at Locations 11.0 and 15.9 than at Locations 2.0 and 5.0 (Mixing Zone)in May and November, and during August 15.9 and 9.5 had significantly higher densities than did the Mixing Zone locations. During February, I Locations 15.9 and 2.0 had significantly lower densities than other locations. These trends were similar to those reported Ibr 1994 (Duke Power Company 1995).

Total epilimnetic densities for February at Locations 5.0 and 9.5 generally increased during the course of the study, especially fiom 1991 to 1995 (Figure 4-2). May zooplankton Q densities for all Lake Norman locations also showed peaks in 1995. This indicates a trend of mereasing zooplankton standing crops for February and May of succeeding years since 1991.

This trend was not reflected in phytoplankton standing crops (Chapter 3). Lakewide, zooplankton densities in August and November showed no consistent long term trends since 1987. j Conununity Composition Seventy zooplankton taxa have been identified since the Lake Norman Maintenance Monitoring study began in 1987 (Table 4-3). Three new taxa were identified in 1995; one copepod. Epischura fluviatilis, and two rotifers, Trichocerca porceHus and T. similis.

Epischura, first observed in a Duke Power reservoir during the 1,ake Keowee 1989-1993 study (Duke Power Company 1994), was never found in previous studies of Lake Norman.

O 4-3

l i

Both of the rotifers were recorded from Lake Norman prior to the current study (Hamme 1982).

Rotifers were the most abundant and diverse group during 1995, as has been the case in previous studies (Table 4-1, Figures 4-3 and 4-4). Copepods dominated zooplankton l epilimnetic assemblages at Location 2.0 in May, and Location 5.0 in August, and they ,

dominated whole column samples at these locations in May and August (Table 4-1).

Cladocerans were never numerically dominant during 1995.

Rotifers demonstrated a spatial pattern of increasing densities from downlake to uplake locations in all but February. This pattern was also documented by llamme (1982) in earlier studies on Lake Norman. Copepods and cladocerans showed no consistent seasonal trends in 1995 (Table 4-1, Figure 4-3).  !

l O i I

l I

Srnchaeta most often dominated rotifer populations in February; with Keratella, Pv/yarthra, and Trichocerca important at some locations. In May, Keratella was the dominant rotifer at all but Location 2.0, where Pv/yarthra was the dominant taxon. Rotifer populations in August were dominated by Trichocerca at all but Location 15.9, where Kerate//a and Canachilus dominated epilimnetic and whole column samples, respectively. In November, Polyarthra was the dominant rotifer at all but Location 15.9, where Kerotella was most j abundant. These patterns of seasonal rotifer abundance were similar to those observed in previous studies (Duke power Company 1988,1989,1990,1991,1992,1993,1994, and 1995; Ilamme 1982). ,

Long term tracking of rotifer populations indicated some notable seasonal patterns since 1992 with peak mean densities at Mixing Zone and Background locations in May of 1992 and l O ' 993, ""a ve8<""<r i 994. ""<i"8 i995 ae"eitie' "' "ixi"8 ze"e iee" tie"' ne8'ea i" 4-4

February; while those at the Backround locations peaked in May (Figure 4-4). The highest mean density from llackground locations since 1990 was observed in May 1995; while the highest mean Mixing Zone density during this six year period occurred in February 1995.

Copepod populations were consistently dominated by immature forms (primarily nauplii, and occasionally cyclopoid copepodites) during 1995, as has always been the case. Tropocyclops, Mesocyclops, and Cyclops were often important constituents of adult populaiions, but adult copepods seldom comprised more than 5 % of the total zooplankton density at any location throughout 1995. Seasonal trends of copepod densities were quite apparent. Annual peaks generally occurred in May, and minimum values were noted in August (Figure 4-4).

4 Bosmina was the most abundant cladoceran observed in 1995 samples, as has been the case in most previous studies (Duke Power Company 1995, llamme 1982). Bosmina often comprised greater than 5 % of the total zooplankton densities in both epilimnetic and whole column samples, and was the dominant zooplankton taxon in the epilimnion at Location 2.0 in November 1995. Bosminopsis and Diaphonosoma were also important at Locations 5.0 and 11.0 in August. Seasonal trends of cladoceran densities were variable. From 1990 to 1993, peak densities occurred in February; while in 1994 and 1995, maxima were recorded in May. The highest mean llackground density in six years was noted in May 1995 (Figure 4-4).

FUTUlm STilDIES No changes are planned for the zooplankton portion of the Lake Norman maintenance .

monitoring program in 1996.

O 4-5

4 f

SUMMARY

1

Total zooplankton standing crops were generally highest in May and lowest in August, and 4

densities were most ollen higher in epilimnetic samples than whole column samples. With the exception of February, zooplankton densities were higher among Backgroud locations i

than at Mixing zone locations, as was the case in 1994. Comparisons of each quarter from year to year showed that epilimnetic zooplankton densities from most Lake Norman locations i in February and May peaked in 1995, indicating long term increases in zooplankton 4

productivity during these months since 1991. In August and November of 1995, zooplankton densities were within historical ranges.

1 Overall, rotifers dominated zooplankton standing crops throughout most of 1995, followed l closely by copepods, as has been documented previously. Since 1990, rotifers most often t.

peaked in February and May; while copepods were generally most abundant in May.

Cladocerans never dominated zooplankton densities in 1995. Over the long term, cladoceran i

densities peaked in February of 1990-1993, and in May 1994-1995. Major rotifer taxa observed in 1995 were Synchaeta, Keratella, Polyarthra, and Trichocerca. Copepod i populations were dominated by immature forms, with adults seldom accounting for more than 5 % of zooplankton densities Bosmina was the predominant cladoceran taxon of 1995.

s

~

Trends in community composition and taxon abundance were similar to those observed i during previous studies.

i J  !

4 1.lTERATURE CITED i

. 1 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. McGuire Nuclear Station,316(a) Demonstration. Duke Power Company, Charlotte, NC.

O 4-6

i Duke Power Company.1988. Lake Nonnan Maintenance monitoring program: 1987 Summary. Duke Power Company, Charlotte, NC.

Duke Power Company.1989. Lake Norman Maintenance monitoring program: 1988 Summary. Duke Power Company, Charlotte, NC.

Duke Power Company.1990. Lake Norman Maintenance monitoring program: 1989 Summary. Duke Power Company, Charlotte, NC.

l l Duke Power Company.1991. Lake Norman Maintenance monitoring program: 1990 Summary. Duke Power Company, Charlotte, NC.

l Duke Power Company.1992. Lake Norman Maintenance monitoring program: 1991 Summary. Duke Power Company, Charlotte, NC.

Duke Power Company.1993. Lake Norman Maintenance monitoring program: 1992 -

Summary. Duke Power Company, Charlotte, NC.

Duke Power Company.1994. Lake Nonnan Maintenance monitoring program: 1993 Summary. Duke Power Company, Charlotte, NC.

Duke Power Company.1995. Lake Nonnan Mainteuance monitoring program: 1993 O Summary. Duke Power Company, Charlotte. NC.

Duke Power Company.1995. Oconee Nuclear Station 316(a) Demonstration Report. Duke Power Company. Charlotte, NC 1

llamme, R. ii.1982. Zooplankton, b J. E. Ilogan and W. D. Adair (eds.). Lake Norman Summary, Technical Report DUKEPWR/82-02. p. 323-?53. Duke Power Company, Charlotte, NC. 460 p.

Ilutchinson, G. E 1967. A Treatise on Limnology. Vol.11. Introduction to Lake Biology and the Limnoplankton. John Wiley and Sons,Inc. N. Y. I115 pp.

Menhinick, E. F. and I.. D. Jemen.1974. Plankton populations. lu L. D. Jensen (ed.).

Environmental responses to thennat dischaiges 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 llopkins University, Baltimore. MD 235 p.

O 4-7

(~ Table 4-1. Total zooplankton densities (no. x 1000/m3) , densities of major zooplankton taxonomic groups, and percent composition (in parentheses) of major taxa in 10m to surface (10-S) and bottom to surface (B-S) net tow samples collected from Lake Norman in February, May, August, and November 1995.

Sample Locations Date Tyng Taxon 2.0 5.0 9.5 11.0 15 9 02/27/95 10-S COPEPODA 15.8 15.8 75.5 26.2 10.!

(35.7) (10.9) (41.0) (31.2) (46.1 )

CLADOCERA 2.0 1.8 12.0 10.7 15 (4.0) (1.9) (6.5) (12.7) (GG)

ROTIFERA 26.4 7G.0 96.7 47.1 10.5 (59.7) (81.2) (52.4) (50.1) (47.1)

, TOTAL 44.3 93.6 184.2 84.0 22.2 B-S COPEPODA 14.5 13.3 48.5 27.1 12.5

. depth (m) (37.0) (18.8) (38.3) (44.9) (43.3)

I of tow for each CLADOCERA 2.2 3.1 6.1 5.5 1.8 location (5.0) (4.4) (4.8) (9.2) (6.2) 2.0=29 l 5.0= 18 ROTIFERA 22.4 54.1 72 0 27.7 14.5 1 i

p 9.6=20 (57.4) (76.2) (56.8) (45.9) (50.5)

Q 11.0=25 15.9:20 TOTAL 39.2 70.5 126.6 60.4 28.8 1

i 05/31/95 10-S COPEPODA 57.1 37.4 25.5 52.7 37.6 (52.7) (39.4) (22.4) (23.2) (14.8)

CLADOCERA 17.2 13.7 9.0 33.0 52.0 (15.8) (14.4) (7.9) (14.5) (20.4)

ROTIFERA 34.3 43.9 79.2 141.9 164.9 (31.4) (40.2) (69.0) (62.3) (64.8)

TOTAL 109.0 95.0 113.8 227.7 254.6 B.S COPEPODA 33.0 38.6 21.8 28.9 49.7 depth (m) (56.0) (48.1) (28.4) (23.1) (20.6) of tow for each CLADOCERA 16.5 12.7 10.7 25.0 51.2 ~

location (28.4) (15.8) (14.0) (20.0) (21.3 2.0=30 5.0=19 ROTIFERA 8.7 29.0 44.3 71.2 139.8 9.5=20 ( 15.0) (30.0) (57.6) (5G.9) (58.1) 3 11.0=25 '

15.9=15 TOTAL 58.2 80.3 70.8 125.1 240.8 Table 4-1 (continued) Page 2 of 2 4-8  ;

4

_. .___..__._____-.___._-.___.____m....___ . _ _ _ _ - _ _ __ _ . . . . _ . _ _ . _ . . _ _ . . .

Q Date Sample Tyng' Taxon 2.0 Locations 5.Q - 9.5 11.0 15.9 ,

08/30/95 10-S COPEPODA 9.2 18.3 12.4 11.7 9.0 (27.1) (52.2) (24.8) (31.6) (11.1)

CLADOCERA 5.4 4.4 5.1 5.5 16.4

( 16.1) (12.5) (10.3) -(14.9) (20.2)

ROTIFERA 19.1 12.4 32.5 19.8 55.8 (56.8) (35.3) (64.9) (53.4) (68.7) l TOTAL 32.2 35.0 50.1 37.0 81.2 i.

B-S COPEPODA 8.6 17.6 14.3 8.4 10.8 depth (m) (40.3) (60.7) (31.3) (39.0) (13.3) of tow for each CLADOCERA 4.4 - 2.7 6.9 4.6 19.3 location (20.4) (9.4) (15.2) (21.5) (23.7) 2.0=28 5.0=18 ROTIFERA 8.4 8.6 24.4 8.5 51.0 9.5=20 (39.2) (29.8) (53.5) (39.5) (62.9) 11.0=24 15.9=13 TOTAL 21.4 29.0 45.6 21.6 81.1 11/30/95 10.S COPEPODA 13.8 7.0 17.3 36.5 41.6 (29.5) (13.0) (19.1) (27.3) (35.2)

CLADOCERA 9.6 2.9 5.2 10.8 4.5  :

(20.7) (5.4) (5.7) (8.1) (3.8)

HOTIFERA 23.2 43.7 67.9 86.1 72.3 (49.8) (81.6) (75.1) (64.5) (61.0)  ;

TOTAL 46.6 53.6 90.4 133.4 118.4 B-S COPEPODA 17.0 13.7 20.5 31.1 26.6 depth (m) (28.4) (24.4) (25.4) (23.0) (28.7) of tow for each CLADOCERA 21.4 6.3 2.5 15.9 5.8 location (35.7) (11.2) (3.1) (11.8) (6.2) 2 0=30 5.0=18 ROTIFERA 21.6 36.1 57.8 88.0 60.4 9.5=20 (36.0) (64.4) (71.5) (65.2) (65.1) 11.0=25 -

15.9=19 TOTAL 60.0 56.1 80.9 135.0 92.8 O

4-9

- .- . _ . .. . - . _ . - - . .. - - - - =

/'N Table 4-2. Duncan's Multiple Range Test on zooplankton densities in Lake l

O Norman, NC during 1995. (Means connected by the same line are not

significantly different, and zooplanton densities are no. x 1000hn3)

{

i February Location 15.9 2.0 11.0 5.0 9.5-l Mean 22.2 44.3 84.0 93.6 184.2 May Location 5.0 2.0 9.5 11.0 15.9 Mean 95.0 100.0 113.7 227.7 254.G August Location 2.0 5.0 11.0 9.5 15.0 Mean 33.0 35.0 36.9 50.1 81.2 November Location 2.0 5.0 9.5 15.9 11.0 Mean 40.6 53.6 90.4 113.3 133.4 O

.o 4-10

Q Table 4-3. Zooplankton taxa identified from samples collected on Lake Norman quarterly from August 1987 through November 1995 (* indicates new taxa observed in 1995).

COPEPODA Cyclops thomasi S. A. Forbes Chromogaster app. Lauterborne C. spp. Fischer Collotheca spp. Harring Diaptomus birgei Marsh Conochiloides spp. Hlava D. mississippiensis Marsh Conochilus unicornis (Rousselet)

D. pallidus 1Icrick C. spp. Hlava D. spp. Marsh Gastropus spp. Imhof

• Epishura fluviatilis Herrick Hexarthra spp. Schmada Afesocyclops edax (S. A. Yorbes) Kellicatia bostoniensis (Rousselet)

31. spp. Sars K. spp. Rousselet Tropocyclops prasinus (Yischer) Keratella spp. Bory de St. Vincent T. spp. Kiefer Lecane spp. Nitzsch Calenoid copepodites Afacrocheatus spp. Perty Cyclopoid copepodites Afonostyla stenroosi(Meissener)

Nauplii Af. spp. Ehrenberg Plocosoma hedsorti Brauer CLADOCERA P. truncatum (Levander)

P. spp. Herrick Bosmina longirostris (O. Y. Muller) Polyarthra euryptera (Weirzeiiski)

B. spp. Baird P. vulgaris Carlin Bosminopsis dictersi Richard P. spp. Ehrenberg Ceriodaphnia spp. Dan 1 Ptygura spp. Ehrenberg Chydorus spp. Leach Synchaeta spp. Ehrenberg  ;

Daphnia ambigua Scourfield Trichocerca capucina (Weireijski)

D. lumholzi Sars T. cylindrica (1mhof)

D. parvula Yordyce

• T. porcellus (Gosse)

D. spp. Mullen T. similis Lamark Diaphanosoma spp. Yischer T. spp. Lamark Holopedium amazonicum Stingehn Unidentified Bdelloidea H. spp. Stingelin (splodora kindtii (Voche) 1NSECTA Lydigia spp. Freyberg j Byocryptus sordidus (Lieven) Chaoborus spp. Lichtenstein

1. spp. Sars Sida crystallina O. Y. Muller ROTIFERA Anuracopsis spp. Iauterborne Asplanchna spp. Gosse Brachionus caudata Barrois and Daday ,

B. havanuensis Rousselet i B. patulus O. F. Muller B. spp. Pallas D

U -

4-1i

l l

l

% 1 10m TO SURFACE TOWS I l

l i

l 300 _ _ _ . _ .

l l

l 250 l l

200 7

2 g 150 9O

• 100 I Ol 1 l 20 50 95 11.0 15 9 I

l l

BOTTOM TO SURFACE TOWS A

t/ :n _ _ _ _ . _ _ _ _ _ _ _ _ _ . _ . _ _ _ _ _ . _ _ _ - _ _ - _ _ - _ . _

1 25C i

200 l 7 I 5  !

g 150 9

100  %

N e a E

50 V Ol W' q E

20 50 95 11 0 15 9 LOCATIONS

% FEB _g. MAY _e- AUG -e NOV Figure 4-1. Total zooplankton density by location ihr samples collected in Lake Norman, NC in 1995.

n,

(

4-12

I l

I

/ 'N l V MIXING ZONE FEBRUARY MAY 300 300 _.

+ 2 0 -g . 5 0 250 250 n n

, E 200 E 200 l 9 5

e x x 6 150 6 150 e c D D 100 100 50 50 1

O - .._ _ -- 0 87 88 89 90 91 92 93 94 95 87 88 89 90 91 92 93 94 95 BACKGOUND LOCATIONS E

300

_ . . _ . _ _ _ . _ _ . . _ -._, . 9 5 . g 110 - g 15 9._ _ - _

- - - agg-- --- - - - -- ,l l t 210 A

) 250 v /

_ _ /i ya 7m /l a a S E k '

k 6 150  ; 6 150 C C D D 100  ! 100 8 ./ N, 8 s N

x.

i l

m / i m i l O a o

87 88 89 90 91 92 93 94 95 88 89 90 91 92 93 M 95 87 YEARS yg3 Figure 4 2. Total zooplankton tiensity by location for epilimnetic samples collecte<l in Lake Norman, NC in 1995.

1 1

0 vi 4-13

,m (s)

MYJNG ZOtE AUGUST POVEMBER 300 . . . _ .-.. 300 _-_ _.. . _ . _.

-e 2 0 -e 50 250 . 250 l

?= Tm N N O E x x 6 12 6 150 e e a e 6 100 6100 0 3 O

, j  !

0 0 87 88 89 90 91 92 93 94 95 87 88 89 90 91 92 93 94 95 EMCKGOutO LOCATIONS

~

. _e e 5 -a 110 --. 15 9 b ,

\

?w a >

i in, a

O,

' O h {

dIT l dI n n

~i 100 100 d s s

'8

/ / g 8 4

J l N \

0 o 87 88 89 (A 91 92 93 94 95 87 88 89 90 91 92 93 94 95 YEARS YEARS Figure 1-2 (continued).

x 4-14

l l

10 v

FEBRUARY MAY l 200 300 180 160 2w i"

h 120

im ISO 80 l= '= l 50 E

, 0 0 2.0 50 95 11.0 15 9 2.0 50 95 11 0 15 9 AUGUST NOVEMBER 90 140 120 70 , ,

i r x

,w e

( j 60 1 _

( 7-

'* w

? l l ,0 .

E' .

8 ,

i e Vs E* W in M A a _ m  : cs a g i: 4 e l 40 7 y l$ E h fd

,0 ll '

u g =h5 0 0 20 50 95 11 0 15 9 2.0 50 95 11 0 15 9 LOCATIONS l l COPEPODS .

CLADOCERANS W ~ ROTIFERS Figure 4-3. Zooplankton composition by month for epilimnetic samples collected during 1995 in Lake Norman, NC.

4-15

l

/m')

' 80 . . _ _ _ _ .

O y ODS __~

70 60 50 40 30 20 10 ' \

0 I CLADOCERANS l 36

--e MIXING ZONE 4-., BACKGROUND LOCATIONS 30 y 25 s

[ 20 si l 8 1

{is  !

.- i

!'o 8 . l

["N

o

=f h

I

\/-

- +

1 v

ROTIF E R S tao . _ _ . .- _ _._ _._.

tu l

ioo  ;

so l 60 1

I

.o ,

m ,\' /  !

~. m -

3i!?ii4

5 2 : 5 5

3iET

?!: 2 : 2 35E5?ii3  : y : i ?s: 5ii8?j 9 z

~

Figure 4-4. Comparison of zooplankton densities, averaged for the Mixing Zone, j and 13ackground locations, by group in epilimnetic samples collected from 1990 tbrough 1995.

1 i

l i

7  %

w/ j 4-16

O

() CIIAPTER 5 FISIIERIES l

l INTRODUCTION I In accordance with the NPDES permit for McGuire Nuclear Station (MNS), monitoring of i specific fish population parameters was continued during 1995. The objectives of the fish l monitoring program for Lake Norman during 1995 were to:

• Continue striped bass mortality monitoring throughout the summer.

• Continue a cooperative striped bass condition study with NCWRC to evaluate stocking rates and to determine the feasibility of stocking hybrid striped bass-white bass in Lake Norman.

• Analyze and summarize the 1994-95 Lake Norman creel data and prepare a report on l tish distribution, an$r harvest, pressure, and success.

METilODS AND MATERIAIS The mixing zone was monitored for striped bass mortalities during summer sampling trips on I the lake, and during the last week of July through August specifically to locate dead or dying fish.

Winter gill netting of striped bass was conducted for condition factor determination, as past of the coopertive study with NCWRC. Three suspended gill nets (250-ft each) were fished for two days. Collected striped bass were weighed and measured fbr total length.

Additionally, otoliths were removed for aging the striped bass.

A creel survey was conducted March 1994 through February 1995 on Lake Norman to obtain infonnation about the sport fishery. The statistical analysis of these data has been delayed, .

and a separate creel survey report will be fbrwarded to NCDEHNR for review in early 1997. l l

[v 5-1

RESULTS AND DISCUSSION G(O The MNS mixing zone was surveyed for striped bass mortalities during summer sampling trips on the lake, and during the last week of July through August ,f 1995 specifically to locate dead or dying fish. Only one dead striped bass was observed in.iowe ni.. N', mm during summer 1995.

Winter gill netting for striped bass condition yielded 70 fish ranging in length dom 281 n?.n to 622 mm. Individual fish length, weight, and age of all striped bass collected in the stuoj l were reported to the NCWRC. '

The temporal and spatial pattern of striped bass habitat expansion and reduction in Lake

, Norman during 1995 was well within the historic range (Chapter 2).

FUTURE FISH STUDIES Continue striped bass mortality monitoring throughout the summer.

Continue a cooperative study with NCWRC to evaluate stocking rates and to determine the feasibility of stocking hybrid striped bass-white bass in Lake Norman.

a

[] Cooperate on future (1997) crappie trap netting sady on Lake Nonnan.

s i

e a

5-2

-