ML20216B247
| ML20216B247 | |
| Person / Time | |
|---|---|
| Site: | Vogtle  |
| Issue date: | 12/31/1997 |
| From: | SOUTHERN NUCLEAR OPERATING CO. |
| To: | |
| Shared Package | |
| ML20216B245 | List: |
| References | |
| NUDOCS 9805180010 | |
| Download: ML20216B247 (67) | |
Text
i VOGTLE ELECTRIC GENERATING PLANT RADIOLOGICAL ENVIRONMENTAL OPERATING REPORT FOR 1997 f r:
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TABLE OF CONTENTS Section and/or Title Subsection Page List of Figures ii List of Tables iii List of Acronyms iv 1.0 Introduction 1-1 2.0 REMP Description 2-1 3.0 Results Summary 3-1 4.0 Discussion of Results 4-1 ,
4.1 Land Use Census and River Survey 4-5 4.2 Airborne 4-7 4.3 Direct Radiation 4-10 4.4 Milk 4-14 4.5 Vegetation 4-16 4.6 River Water 4-18 4.7 Drinking Water 4-21 l 4.8 Fish 4-27 4.9 Sediment 4-30 .
5.0 Interlaboratory Comparison 'l Program (ICP) 5-1 l
6.0 Conclusions 6-1 I
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LIST OF FIGURES Figure Number Title Page >
Figure 2-1 REMP Staticas in the Plant Vicinity 2-10 Figure 2-2 REMP Control Stations for the Plant 2-11 Figure 2-3 REMP Indicator Drinking Water Stations 2-12 Figure 4.2-1 Average Weekly Gross Beta Air Concentration 4-8 Figure 4.3-1 Average Quarterly Exposure from Direct Radiation 4-11 Figure 4.3-2 Average Quarterly Exposure from Direct Radiation at SpecialInterest Areas 4-12 Figure 4.4-1 Average Annual Cs-137 Concentration in Milk 4-14 Figure 4.5-1 Average Annual Cs-137 Concentration in Vegetation 4-17 Figure 4.6-1 Average Annual H-3 Concentration in River Water 4-20 Figure 4.7-1 Average Monthly Gross Beta Concentration in Raw Drinking Water 4-22 Figure 4.7-2 Average Monthly Gross Beta Concentration in Finished Drinking Water 4-23 Figure 4.7-3 Average Annual H-3 Concentration in Raw Drinking Water 4-25 Figure 4.7-4 Average Annual H-3 Concentration in Finished Drinking Water 4-26 Figure 4.8-1 Average Annual Cs-137 Concentration in Fish 4-28 Figure 4.9-1 Average Annual Be-7 Concentration in Sediment 4-31 Figure 4.9-2 Average Annual Co-58 Concentration in Sediment 4-32 Figure 4.9-3 Average Annual Co-60 Concentration in Sediment 4-33 Figure 4.9-4 Average Annual Cs-137 Concentration in Sediment 4-34 1 1
i ll
LIST OF TABLES Table Number Title Page Table 2-1 Summary Description of Radiological Environmental Monitoring Program 2-2 Table 2-2 Radiological Environmental Sampling Locations 2-7 Table 3-1 Radiological Environmental . Monitoring Program Annual Summary 3-2 Table 4-1 Minimum Detectable Concentrations (MDC) 4-1 Table 4-2 Reporting Levels (RL) 4-2 Table 4-3 Deviations from Radiological Environmental Monitoring Program 4-4 Table 4.1-1 Land Use Census Results 4-5 Table 4.2-1 Average Weekly Gross Beta Air Concentration 4-8 Table 4.3-1 Average Quarterly Exposure from Direct Radiation 4-11 Table 4.3-2 Average Quarterly Exposure from Direct Radiation at SpecialInterest Areas 4-13 Table 4.4-1 Average Annual Cs-137 Concentration in Milk 4-15 Table 4.5-1 Average 6ual Cs-137 Concentration in Vegetation 4-17 Table 4.6-1 Average Annual H-3 Concentration in River Water 4-20 Table 4.7-1 Average Monthly Gross Beta Concentration in Raw Drinking Water 4-22 Table 4.7-2 Average Monthly Gross Beta Concentration in Finished Drinking Water 4-23 Table 4.7-3 Average Annual H-3 Concentration in Raw Drinking Water 4-25 Table 4.7-4 Average Annual H-3 Concentration in Finished Drinking Water 4-26 Table 4.8-1 Average Annual Cs-137 Concentration in Fish 4-28 Table 4.9-1 Average Annual Be-7 Concentration in Sediment 4-31 Table 4.9-2 Average Annual Co-58 Concentration in Sediment 4-32 Table 4.9-3 Average Annual Co-60 Concentration in Sediment 4-33 Table 4.9-4 Average Annual Cs-137 Concentration in Sediment 4-34 Table 4.9-5 Additional Sediment Nuclide Concentrations 4-35 Table 5-1 Interlaboratory Comparison Program Results 5-3 iii
i LIST OF ACRONYMS l l
Acronyms presented in alphabetical order.
I Acronym Definition A2LA American Association of Laboratory Accreditation ASTM American Society for Testing and Materials ,_
CL Confidence Level EL Georgia Power Company Environmental Laboratory EPA Environmental Protection Agency GPC Georgia Power Company ICP Interlaboratory Comparison Program MDC Minimum Detectable Concentration l MDD Minimum Detectable Difference MWe Megawatts Electric NA Not Applicable NDM No Detectable Measurement (s)
NRC- Nuclear Regulatory Commission ODCM Offsite Dose Calculation Manual Po Preoperation PWR Pressurized Water Reactor REMP Radiological Environmental Monitoring Program RL Reporting Level RM River Mile TLD Thermoluminescent Dosimeter TS Technical Specification l
VEGP Alvin W. Vogtle Electric Generating Plant i
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1.0 INTRODUCTION
The Radiological Environmental Monitoring Program (REMP) is conde,:ted in accordance with Chapter 4 of the Offsite Dose Calculation Manual (OICM). The REMP activities for 1997 are reported herein in accordance with *fechnical l Specification (TS) 5.6.2 and ODCM 7.1.
l The objectives of the REMP are to:
- 1) Determine the levels of radiation and the concentrations of radioactivity in the environs and;
- 2) Assess the radiological impact (if any) to the environment due to the operation of the Alvin W. Vogtle Electric Generating Plant (VEGP).
l The assessments include comparisons between results of analyses of samples l
! obtained at locations where radiological levels are not expected to be affected by l
plant operation (control stations) and at locations where radiological levels are j
more likely to be affected by plant operation (indicator stations), as well as comparisons between preoperational and operational sample results. j VEGP is owned by Georgia Power Company (GPC), Oglethorpe Power Corporation (OPC), the Municipal Electric Authority of Georgia (MEAG), and the City of Dalton, Georgia. It is located on the southwest side of the Savannah River approximately 23 river miles upstream from the intersection of the Savannah River and U.S. Highway 301. The site is in the eastern sector of Burke County, Georgia, and across the river from Barnwell County, South Carolina. The VEGP site is directly across the Savannah River from the Department of Energy Savannah . River Site. Unit 1, a Westinghouse Electric Corporation Pressurized Water Reactor (PWR), with a rated power output of 1232 Megawatts (MWe),
received its operating license on January 16, 1987 and commercial operation started on May 31,1987. Unit 2, also a Westinghouse PWR rated for 1232 MWe, received its operating license on February 9,1987 and began commercial operation on May 19,1989.
The preoperational stage of the REMP began with initial sample collections in August of 1981. The transition from the pre-operational to the operational stage of the REMP occurred as Unit I reached initial criticality on March 9,1987.
A description of the REMP is provided in Section 2 of this report. Maps showing the sampling stations are keyed to a table which indicates the direction and distance of each station from a point midway between the two reactors. An annual summary of the results of the analyses of REMP samples is provided in Section 3.
A discussion of the results, including assessments of any radiological impacts upon the environment and the results of the land use census and the river survey, is provided in Section 4. The results of the Interlaboratory Comparison Program (ICP) are provided in Section 5. Conclusions are provided in Section 6.
1-1
I 2.0 REMP DESCRIPTION A summary description of the REMP is provided in Table 2-1. This table summarizes the program's requirements as outlined in ODCM Table 4-1 by j detailing the sample types to be collected and the analyses to be performed in order to monitor the airborne, direct radiation, waterborne and ingestion pathways, and also by delineating the collection and analysis frequencies. In addition, Table 2-1 references the locations of stations as described in ODCM Section 4.2 and in Table 2-2 of this report. The stations are also depicted on maps in Figures 2-1 through 2-3.
REMP samples are collected by Georgia Power Company's (GPC) Environmental Laboratory (EL) personnel. The same lab performs all the laboratory analyses at their headquarters in Smyma, Georgia. Since 1987, the EL has been accredited by the American Association of Laboratory Accreditation (A2LA) for radiochemistry. Accreditation is based upon intemationally accepted criteria for laboratory competence (ISO /IEC Guide 25,1990, General Requirements for the Competence of Calibration and Testing Laboratories).
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TABLE 2-2 (SiiEET I of 3)
RADIOLOGICAL ENVIRONMENTAL SAMPLING LOCATIONS Station Station Descriptive Direction' Distan Sample Type Number Type Location (miles)je 1 Indicator Hancock N 1.1 Direct Rad.
Landing Road 2 Indicator River Bank NNE 0.8 Direct Rad.
3 Indicator Discharge Arca NE 0.6 Airborne Rad.
3 Indicator River Bank NE 0.7 Direct Rad 4 Indicator River Bank ENE 0.8 Direct Rad.
5 Indicator River Bank E 1.0 Direct Rad.
6 Indicator Plant Wilson ESE 1.1 Direct Rad.
7 Indicator Simulator SE 1.7 Airborne Rad.
Building Direct Rad.
Vegetation 8 Indicator River Road 'SSE 1.1 Direct Rad.
9 Indicator River Road S 1.1 Diiect Rad.
10 Indicator Met Tower SSW 0.9 Airborne Rad.
10 Indicator River Road SSW l.1 Direct Rad.
I1 Indicator River Road SW l.2 Direct Rad.
12 Indicator River Road WSW l.2 Airborne Rad.
Direct Rad.
13 Indicator 'I(iver Road W l.3 Direct Rad.
14 Indicator River Road WNW l.8 Direct Rad.
15 Indicator Hancock NW l.5 Direct Rad.
Landing Road Vegetation 16 Indicator "ancock NNW l.4 Airbome Rad.
Landing Road Direct Rad.
17 Other Sav. River Site N 5.4 Direct Rad.
(SRS), River Road 18 Other SRS, D Area NNE 5.0 Direct Rad.
19 Other SRS, Road NE 4.6 Direct Rad.
A.13 20 Other SRS, Road ENE 4.8 Direct Rad.
A.13.1 21 Other SRS, Road E 5.3 Direct Rad.
A.17 22 Other River Bank ESE 5.2 Direct Rad.
23 Other River Road SE 4.6 Direct Rad.
24 Other Chance Road SSE 4.9 Direct Rad.
25 Other Chance Road S 5.2 Direct Rad.
near Highway 23 26 Other Higliway 23 SSW 4.6 Direct Rad. ,
and Ebenezer Church Road l 27 Other Highway 23 SW 4.7 Direct Rad.
opposite Boll Weevil Road 28 Other Thomas Road WSW 5.0 Direct Rad.
2-7
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TABLE 2-2 (SilEET 2 of 3)
RADIOLOGICAL ENVIRONMENTAL SAMPLING LOCATIONS Station Statiot Descriptive Direction 8
Distanje Sample Type Number Type Location (miles) 29 Other Claxton-Lively W 5.1 Direct Rad.
Road 30 Other Nathaniel WNW 5.0 Direct Rad.
Howard Road 31 Other River Road at NW 5.0 Direct Rad.
Allen's Chapel Fork 32 Other River Bank NNW 4.7 Direct Rad.
33 Other Hunting Cabin SE 3.3 Direct Rad.
35 Other Girard SSE 6.6 Airborne Rad.
Direct Rad.
36 Control GPC WSW 13.9 Airborne Rad.
Waynesboro Direct Rad.
Op. HQ 1 37 Control Waynesboro WSW 16.7 Direct Rad Substation Vegetation 43 Other Employee's SW 2.2 Direct Rad.
Rec. Center 47 Control Oak Grove SE 10.4 Direct Rad. i j
Church 48 Control McBean NW 10.2 Direct Rad.
Cemetery 80 Control Augusta Water NNW 29.0 Drinkipg Treatment Water Plant 81 Control Sav River N 2.5 Fish' 4 Sediment 82 Control Sav River (RM NNE 0.8 River Water 151.2) 83 Indicator Sav River (RM ENE 0.8 River Wajer 150.4) Sediment 84 Other Sav River (RM ESE 1.6 River Water 149.5) 85 Indicator Sav River ESE 4.3 Fish' 87 Indicator Beaufort-Jasper SE 74 Drinkipg Water I County Water Treatment Plant 88 Indicator Cherokee Hill SSE 71 Drinkipg Water Water l Treatment j Plant, Port j Wentworth, Ga j 98 Control W.C. Dixon SE 9.8 Milk j Dairy l 99 Control Boyceland W 20.9 Milk l Dairy I l
l 2-8 1
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l TABLE 2-2 (SHEET 3 of 3)
RADIOLOGICAL ENVIRONMENTAL SAMPLING LOCATIONS l Notes:
(1) Direction and distance are determined from a point midway between the two two reactors.
(2) The intake for the Augusta Water Treatment Plant is located on the Augusta Canal.
The entrance to the canal is at River Mile (RM) 207 on the Savannah River. The canal effectively parallels the river. The intake to the pumping station is about 4 miles down the canal.
(3) A 5 mile stretch of the river is generally needed to obtain adequate fish samples.
Samples are normally gathered between RM 153 and 158 for up:iver collections and between RM 144 and 149.4 for downriver collections.
(4) Sediment is collected at locations with existing or potential recreational value. Since high water flow, shifting river bottom sediment, or other reasons could cause a suitable location for sediment collections to become unavailable or unsuitable, a stretch of the river between RM 148.5 and 150.5 was designated for downriver collections while a stretch between RM 153 and 154 was designated for upriver collections. In practice, collections are normally made at RM 150.2 for downriver collections and RM 153.3 for upriver collections.
(5) The intake for the Beaufort-Jasper County Water Treatment Plant is located at the end of a canal which begins at RM 39.3 on the Savannah River. This intake is about 16 miles by line of sight down the canal from its beginning on the Savannah River.
(6) The intake for the Cherokee Hill Water Treatment Plant is located on Abercorn Creek which is about one and a quarter creek miles from its mouth on the Savannah River at RM 29.
I i
2-9
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, Radiological Environmental Sampling Locations ina o, coni,a w n u oi REMP Stations in the no i i i Plant Vicinity our e e e TLD & Other o o o Figure 2-1 l 2-10
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RD & Other o o o Figure 2-2 2-11 J
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3.0 RESULTS
SUMMARY
In accordance with ODCM 7.1.2.1, the summarized and tabulated results for all of the regular samples collected for the year at the designated indicator, community and control stations are presented in Table 3-1. The format of Table 3-1 is similar to Table 3 of the Nuclear Regulatory Commission (NRC) Radiological Assessment Branch Technical Position, Revision 1, November 1979. Results for samples collected at any other locations are discussed in Section 4 under the particular sample type.
As indicated in ODCM 7.1.2.1, only the naturally occurring radionuclides found in the plant's effluent releases are required to be reported. The radionuclide Be-7 which occurs abundantly in nature is found in the plants' liquid effluent. No other naturally occurring radionuclides are found in any of the plants' other effluent releases. Therefore, the only radionuclides ofinterest in the samples monitoring liquid releases (surface water, fish, and river sediment) are the man-made radionuclides and Be-7. Only man-made radionuclides are ofinterest for the other REMP samples.
l 3-1
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Y
4.0 DISCUSSION OF RESULTS Included in this section are evaluations of the laboratory results for the various sample types. Comparisons were made between the difference in mean values for pairs of station groups (e.g., indicator and control stations) and the calculated Minimum Detectable DitTerence (MDD) between these pairs at the 99%
Confidence Level (CL). The MDD was determined using the standard Student's t-test. A difference in the mean values which was less than the MDD was considered to be statistically indiscernible.
The 1997 results were compared with past results, including those obtained during preoperation. As appropriate, results were compared with their Minimum Detectable Concentrations (MDC) and Reporting Levels (RL) which are listed in Tables 4-1 and 4-2 of this report, respectively. The required MDC's were achieved during laboratory sample analysis. Any anomalous results are explained within this report.
Results of interest were graphed to show historical trends. The data points are tabulated and included in this report. The points plotted and provided in the tables represent mean values of only detectable results. Periods for which no detectable measurements (NDM) were observed or periods for which values were not applicable (e.g., milk indicator, etc.) were plotted as and listed in the tables as O's.
Table 4-1 Minimum Detectable Concentrations (MDC)
Analysis Water Airborne Fish Milk Grass or Sediment (pCi/I) Particulate (pCi/kg- (pCi/l) Leafy (pCi/kg) or Gases wet) Vegetation (fCi/m3) (pCi/kg-wet)
Gross Beta 4 10 H-3 2000 (a)
Mn-54 15 130 Fe-59 30 260 Co-58 15 130 Co-60 15 130 Zn-65 30 260 Zr-95 30 Nb-95 15 I-131 1(b) 70 1 60 Cs-134 15 50 130 15 60 150 Cs-137 18 60 150 18 80 180 Ba-140 60 60 La-140 15 15 (a) If no drinking water pathway exists, a value of 3000 pCi/l may be used.
(b) If no drinking water pathway exists, a value of 15 pCi/l may be used.
4-1
Table 4-2 Reporting Levels (RL)
Analysis Water Airborne Fish Milk (pCi/l) Grass or (pCi/l) Particulate (pCl/kg-wet) Leafy or Gases Vegetation (fCi/m3) (pCi/kg-wet) 11-3 20,000 (a)
Mn-54 1000 30,000 Fe-59 400 10,000 Co-58 1000 30,000 :
Co-60 300 10,000 Zn-65 300 20,000 Zr-95 400 !
Nb-95 700 1-131 2 (b) 900 3 100 i Cs-134 30 10,000 1000 60 1000 Cs-137 50 20,000 2000 70 2000 Ba-140 200 300 La-140 100 400 1
(a) This is the 40 CFR 141 value for drinking water samples. If no drinking water pathway exists, a value of 30,000 may be used.
(b) If no drinking water pathway exists, a vt 'ue of 20 pCi/l may be used.
Atmospheric nuclear weapons tests frori the mid 1940's through 1980 distributed man-made nuclides around the world. The most recent atmospheric tests in the 1970's and in 1980 had a significain impact upon the radiological concentrations found in the environment prior t<, and during preoperation, and the earlier years of operation. Some long lived radonuclides, such as Cs-137, continue to have some impact. A significant component of the Cs-137 which has often been found in various samples over the years (and continues to be found) is attributed to the nuclear weapons tests.
Data in this section has been modified to remove any obvious non-plant short term impacts. The specilic short term impact data that has been removed includes: the nuclear atmospheric weapon test in the fall of 1980; abnormal relm, from the Savannah River Site (SRS) during 1987 and 1991; and the Chernot . . sident in the spring of 1986.
In accordance with ODCM 4.1.1.2.1, deviations from the required sampling schedule are permitted, if samples are unobtainable due to hazardous conditions, unavailability, inclement weather, equipment malfunction or other just reasons.
Deviations from conducting the REMP as described in Table 2-1 are summarized in Table 4-3 along with their causes and resolutions.
4-2
All results were tested for conformance to Chauvenet's criterion (G. D. Chase and J. L. Rabinowetz, Principles of Radioisotope Methodolosy, Burgess Publishing Company,1962, pages 87-90) to identify values which dif fered from the mean of a set by a statistically significant amount. Identified outliers were investigated to determine the reason (s) for the difference. If equipment malfunction or other valid physical reasons were identified as causing the variation, the anomalous result was excluded from the data set as non-representative. No data were excluded exclusively for failing Chauvenet's criterion. Data exclusions are discussed in this section under the appropriate sample type.
l i
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I l 4.1 Land Use Census and River Survey i l In accordance with ODCM 4.1.2, a land use census was conducted to determine the i locations of the nearest permanent residence, milk animal, and garden of greater than 500 square feet producing broad leaf vegetation, in each of the 16 compass sectors within a distance of 5 miles; the locations of the nearest beef cattle in each ,
i sector were also determined. A milk animal is a cow or goat producing milk for l l
human consumption. Land within SRS was excluded from the census. No milk i 1
animals were found within a 5 mile distance from the plant. The census results are tabulated in Table 4.1-1.
Table 4.1-1 LAND USE CENSUS RESULTS ;
1 Distance in Miles to the Nearest Location in Each Sector i
SECTOR RESIDENCE MILK BEEF GARDEN ANIMAL CATTLE N none none none none none ;
NNE none none none 1
NE none none none none ENE none none none none E none none none none ESE 4.2 none none none SE 4.3 none none 4.9 SSE 4.6 none 4.3 none l S 4.3 none none 4.4 l SSW 4.7 none 4.6 none SW 2.8 none none none WSW l.2 none 2.7 none W 3.7 none 4.5 none 1 WNW l.7 none 1.7 none j NW l.6 none 1.8 4.2 NNW l.5 none none none ODCM 4.1.2.2.1 requires a new controlling receptor to be identified, if the land use census identifies a location that yields a calculated receptor dose greater than the one !
in current use. It was determined that no change in the controlling receptor was l i required in 1997.
l l I l ODCM 4.1.2.2.2 requires that whenever the land use census identifies a location l which yields a calculated dose (via the same ingestion pathway) 20% greater than that of a current indicator station, the new location must become a REMP station (if samples are available). None of the identified gardens yielded a calculated dose 20% greater than that for any of the current indicator stations.
45
A survey of the Savannah River downstream of the plant for approximately 100 miles was conducted on September 16 to identify any withdrawal of water from the river for drinking or irrigation purposes. No such usage was identified. These results were corroborated by checking with the Georgia Department of Natural Resources and the South Carolina Department of Health and Environmental Control. Each of these agencies confirmed that no water withdrawal permits for drinking or irrigation purposes had been issued for this stretch of the Savannah River. The two water treatment plants used as indicator stations for drinking water are located funher downriver.
i i
l l
4-6
4.2 Airborne l
As specified in Table 2-1 and shown in Figures 2-1 through 2-3, airborne particulate i filters and charcoal canisters are collected weekly at 5 indicator stations (Stations 3, 7,10,12 and 16) which encircle the plant at the site periphery, at a nearby community station (Station 35) approximately 7 miles from the plant, and at a control station (Station 36) which is approximately 14 miles from the plant. At each location, air is continuously drawn through a glass fiber filter to retain airbome particulate and an activated charcoal canister is placed in series to adsorb radiciodine.
Each particulate filter is counted for gross beta activity. A quarterly gamma isotopic i
analysis is performed on a composite of the air particulate filters for each station.
Each charcoal canister is analyzed for I-131.
As prpvided in Table 3-1, the annual average weekly gross beta activity of 20.6 fCi/m for the indicator stations was equal to the control stations' averge to 3 significant digits. The indicator stations' average was actually 0.064 fCi/m greater than that for the control stations; however, this difference if not statistically discemible, since it is less than the calculated MDD of 2.46 fCi/m .
The historical trending of the average weekly gross beta air concentrations for each year of operation and the preoperational period (September,1981 to January,1987) at the indicator, control and community stations is plotted in Figure 4.2-1 and listed in Table 4.2-1. In general, there is a close agreement between the results for the indicator, control and community stations. This close agreement supports the position that the plant is not contributing significantly to the gross beta concentrations in air.
The table and graph show the average concentrations for all the station groups were relatively flat for the 9 year period (1989 through 1997), except that the 1996 average for the indicator stations was a little higher. This was due to a single measurement of 527 fCi/m3 at one of the indicator stations. Plant releases were ruled out as a cause; however, laboratory contamination was a possibility. If this result were excluded, the average for the indicator stations would become 21.4 fCi/m3 which is only 0.4 fCi/m3 greater than the control station average and the difference would not be statistically discernible since it is less than the MDD of 1.9 fCi/m3.
(
4-7
Figure 4.2-1 Average Weekly Gross Beta Air Concentration 30 25
' A '
20 - '
S ]'
[
'N 6 15 1!
i'*
? 1 8 !
5 0
Po 87 88 89 90 91 92 93 94 95 96 97 l
Year )
l-4-Indicator -G-Control -e-Community MOC l Table 4.2-1 Average Weekly Gross Beta Air Concentration Period Indicator (fCi/m3) Control Community (fCi/m3) (fCi/m3)
Pre-op 22.9 22.1 21.9 l 1987 26.3 23.6 22.3 1988 24.7 23.7 22.8 1989 I 9. I 18.2 18.8 1990 19.6 19.4 I 8.8 1991 19.3 19.2 18.6 1992 18.7 19.3 18.0 1993 21.2 21.4 20.3 1994 20.I 20.3 19.8 1995 21.1 20.7 20.7 1996 23.3 21.0 20.0 1997 20.6 20.6 19.0 4-8
)
l During 1997, no man-made radionuclides were detected from the gamma isotopic analysis of the quarterly composites of the air particulate filters. In 1937, Cs-137 was found in one indicator composite at a concentration of 1.7 fCi/m . During preoperation, Cs-137 was found in an eighth of the indicator composites and a sevenp of the control composites with average concentrations3 of 1.7 and 1.0 fCi/m , respectively. The MDC for airborne Cs-137 is 60 fCi/m . Also, during preoperations, Cs-134 was found in about 8% of the indicator cgmposites. The average Cs-134 concentration was 1.2 fCi/m3. Its MDC is 50 fCi/m .
Airborne I-131 was not detected in any sample during 1997. During preoperation, positive results were obtained only during the Chernobyl incident when concentrations as high as 182 fCifm were observed. The MDC and RL for airborne I-131 are 70 and 900 fCi/m , respectively.
During 1997, there were 3 local power outages lasting several hours that affected the same 4 stations. These program deviations are summarized in Table 4-3. The gross beta results for all of the affected samples were checked for conformance with Chauvenet's criterion. Only the results for the Station 10 sample collected on August 19 failed to conform with Chauvenet's criterion. As a result of this failure, both the gross beta analysis of the particulate filter and the I-131 analysis of the charcoal canister were excluded from the data set.
t 4-9
i l
4.3 Direct Radiation Direct (external) radiation is measured with thermoluminescent dosimeters (TLDs). Two Panasonic UD-814 TLD badges are placed at each station. Each badge contains three phosphors composed of calcium sulfate crystals (with thulium impurity). The gamma dose at each station is based upon the average readings of the phosphors from the two badges. The badges for each station are placed in thin plastic bags for protection from moisture while in the field. The badges are nominally exposed for periods of a quarter of a year (91 days). An inspection is performed near mid-quarter to assure that all badges are on-station and to replace any missing or damaged badges.
Two TLD stations are established in each of the 16 compass sectors, to form 2 concentric rings. The inner ring (Stations 1 through 16) is located near the plant perimeter as shown in Figure 2-1 and the outer ring (Stations 17 through 32) is located at a distance of approximately 5 miles from the plant as shown in Figure -
2-1. The 16 stations forming the inner ring are designatec as the indicator stations. 1 The two ring configuration of stations was established in accordance with NRC Branch Technical Position, Revision 1, November 1979. The 4 control stations (Stations 36,37,47 and 48) are located at distances greater than 10 miles from the plant. Monitored special interest areas consist of: Station 33 at a hunting cabin, Station 35 at the town of Girard, and Station 43 at the employee recreational area.
As provided in Table 3-1 the average quarterly exposure measured at the indicator and control stations during 1997 were identical to 3 significant figures. The average for the indicator stations was actually 0.021 mR less than that for the control stations. However, this difference was not statistically discernible since it i was less than the MDD of 1.04 mR. Over the operational history of the site, the i annual average quarterly difference between thedicator m, exposures and control showed stations.a variation of no The overall more than C.7 mR average quarterly exposure for the control stations during preoperation was 1.2 mR greater .
than that for the indicator stations. l The quarterly exposures acquired at the outer ring stations during 1997 ranged !
from 10.4 to 19.3 mR with an average of 13.09 mR which was 0.07 mR greater than that for the inner ring stations. However, this difference was not discernible since it was less than the MDD of 0.76 mR. For the entire period of operation, the annual average quarterly exposures at the inner ring stations varied by no more l than 0.9 mR from those at the outer ring stations. The overall average quarterly i exposure for the inner ring stations during preoperation was 0.6 mR greater than that for the outer ring stations.
The historical trending of the average quaderly exposures for the indicator inner ring, outer ring, and the control stations are plotted in Figure 4.3-1 and listed in Table 4.3-1. The decrease between 1991 and 1992 values is attributed to a change ,
in TLDs from Teledyne to Panasonic. It should be noted however that the differences between indicator and control and outer ring values did not change.
The close agreement between the station groups su,pports the position that the plant is not contributing significantly to direct radiation m the environment.
4-10
l l
Figure 43-1 Average Quarterly Exposure from Direct Radiation 2o I k 14 V \
_ 12 g
\ .
.. # 1 10 8
$8 6
4 2
0 Po 87 88 89 90 91 92 93 94 95 96 97 Year
-+-- Indicator + Control -*- Outer Ring Table 43-1 Average Quarterly Exposure from Direct Radiation Period Indicator Control Outer Ring (mR) (mR) (mR)
Pre-op 15.3 16.5 14.7 1987 17.6 17.9 16.7 _
1988 16.8 16.1 16.0 1989 17.9 18.4 17.2 1990 16.9 16.6 16.3 1991 16.9 17.I 16.7 1992 12.3 12.5 12.I 1993 12.4 12.4 12.I 1994 12.3 12.I i 1.9 1995 12.0 12.5 12.3 1996 12.3 12.2 12.3 1997 13.0 _
13.0 13.1 4-11
6 i
The historical trending of the average quarterly exposures at the special interest areas for the same periods are provided in Figure 4.3-2 and listed in Table 4.3-2.
These exposures are within the range of those acquired at the other stations. They too, show that the plant is not contributing significantly to direct radiation at the special interest areas.
Figure 4.3-2 Average Quarterly Exposure from Direct Radiation at Special Interest Areas 25 g MN "
Mk N :#\
g ,, :
/ .. _.
/ #
I
$ l _
g . . .. .
@ 10 5
0 Po 87 88 89 90 91 92 93 94 95 96 97 Year l --+- Hunting Cabin (Sta 33) --m-Girard (Sta 35) -*- Roc Center (Sta 43) l 4-12 l
l Table 43-2 Average Quarterly Exposure from Direct Radiation at Specia1 Interest Areas Period Station 33 Station 35 Station 43 (mR) (mR) (mR)
Pre-op 16.6 15.I 15.3 1987 21.3 18.5 15.2 1988 19.7 18.I 14.8 1989 21.2 18.7 17.4 1990 16.8 18.9 16.2 ;
1991 17.3 19.6 17.0 1992 12.8 13.5 12.0 1993 12.9 13.3 12.I 1994 12.6 13.6 12.0 1995 13.3 13.5 12.3 1996 13.0 13.6 12.1 1997 13.8 14.4 12.7 The hunting lodge activities at Station 33 have been discontinued. Consequently, this location is no longer considered as an area of special interest. Beginning with the third quarter of 1997, TLDs were placed on a trial basis at the SGA Elementary School in Sardis, Ga. (S at i1.5 miles) and near the center of Alexander, Ga. (SW at 10.4 miles). The quarterly doses found at these two locations were within the range of those found at the control stations during the year. It is planned to discontinue Station 33 and add the Sardis and Alexander locations as additional control stations.
There was one failure in obtaining a measurement of the c uarterly gamma dose during 1997. This occurred at Station 9 during the fourti quarter where both badges became warped due to the heat from a brush fire ad could not be read.
This deviation is listed in Table 4-3.
In addition, the readings for 4 badges (TLDs 0298 & 030B for the third quarter and TLDs 032B & 0438 for the fourth quarter) were deemed unacceptable since the standard deviation for each badge was greater than the self imposed limit of 1.4. Consequently, only the readings for the companion badges were used for determining the quarterly dose in these cases. eason was determined for the high standard deviation. The badges were visudly inspected under a microscope and the glow curve and test results for the anneal data and the element correction factors were reviewed.
The standard deviation for the quarterly result for each badge was subjected to a selfimposed limit of 1.4. This limit is based upon the standard deviations obtained with the Panasonic UD-814 badges during 1092 and is calculated using a method developed by the American Society of Testing and Materials (ASTM Special Technical Publication 15D, ASTM Manual on Presentation of Data and Control Chart Analysis, Fourth Revision, Philadelphia, PA, October 1976).
The limit serves as a flag to initiate an investigation. To be conservative, readings with a greater standard deviation are deleted since the high standard deviation is interpreted as an indication of a suspect TLD.
4 13
i l 4.4 Milk In accordance with Tables 2-1 and 2-2, milk samples are collected biweekly from j
two control locations, the W. C. Dixon Dairy (Station 98) and the Boyceland Dairy l
(Station 99). Gamma isotopic and I-131 analyses are performed on each sample.
No indicator station (a location within 5 miles of the plant) for milk has been available since April 1986. As discu', sol in Section 4.1, no milk animals were found during the 1997 land use census.
No man-made radionuclides were identified during the gamma isotopic analysis of the milk samples in 1997. The MDC and RL for Cs-137 in milk are 18 and 70 pCi/1, respectively. During preoperation and each year of operation through 1991, Cs-137 was found in 2 to 6% of the samples at concentrations ranging from 5 to 27 pCi/1. During preoperation, Cs-134 was detected in one sample and in the first year of operation, Zn-65 was detected in one sample. Figure 4.4-1 and Table 4.4-1 provide the historical trending of the Cs-137 concentration in milk.
Figure 4.4-1 Average Annual Cs-137 Concentration in Milk 20 l
18!
16 g,, \\ / N .
1,, \\ / \
Ji,, \\ / \
3,. \ \ / \
l, \ N :
\
". \ \
2 \ \'
0 Po 87 88 89 90 91 92 93 94 95 96 97 Year
-+-indicator -e-control neocl 4-l4
a l Table 4.4-1 Average Annual Cs-137 Concentration in Milk Year Indicator Control (pCi/l) (pCi/l) ,
Pre-op 18.5 18 1987 0 10.4 1988 0 6.9 1989 0 7 1990 0 17 1991 0 14.2 1992 0 0 1993 0 0 1994 0 0 1995 0 0 1996 0 0 1997 0 0 During 1997, I-131 was not detected in any of the milk samples. Since operations began in 1987, 1-131 may have been detected in one sample in 1996 and two during 1990; however, its presence in these cases was questionable, due to large counting uncertainties. During preoperation, positive 1-131 results were found only during the Chernobyl incident with concentrations ranging from 0.53 to 5.07 pCi/1. The MDC and RL for I-131 in milk are 1 and 3 pCi/1, respectively.
4-15 I - - _ _ _ - _ _
i 4.5 Vegetation In accordance with Tables 2-1 and 2-2, grass samples are collected monthly at two indicator locations onsite near the site boundary (Stations 7 and 15) and at one control station located about 17 miles from the plant (WSW - Station 37). Gamma isotopic analyses are performed on the samples.
Cs-137 was detected in two of the samples in 1997. The average concentration was 32.6 pCi/kg-wet. Both of these samples were collected at the control station approximately 17 miles from the plant, so plant contribution is unlikely. The historical trending of the average concentration of Cs-137 at the indicator and control stations is provided in Figure 4.5-1 and listed in Table 4.5-1. No trend is recognized in these data. The MDC and RL for Cs-137 in vegetation samples are 80 and 2000 pCi/kg-wet, respectively. Cs-137 is the o'lly manmade radionuclide which has been identified in vegetation samples during the operational history of the plant. During preoperation, Cs-137 was found in approximately 60% of the samples from indicator stations and in approximately 20% of the samples from the control station. These fractions have generally decreased during operation.
On a trial basis, grass samples were also collected at two additional indicator locations during the first six months of 1997. One location was just north of Plant Wilson (E at 0.9 miles) and the other was adjacent to Gate 1 (SW at 1.2 miles). In one of the Plant Wilson samples, Cs-137 was found at a concentration of 61.1 pCi/kg-wet. There were no other detectable results in these trial samples.
In 1986 during preoperation, as a consequence of the Chernobyl incident, I-131 -
was found in nearly all the samples collected for a period of several weeks in the range of 200 to 500 pCi/kg-wet. The MDC and RL for I-131 in vegetation are 60 and 100 pCi/kg-wet, respectively. During this time period Co-60 was found in one of the samples. l l
4-16
Figure 4.5-1 l
Average Annual Cs-137 Concentration in Vegetation 180 1 R 160
,, o / \
1 /\ / \
i,,,,
,, .. / \ / \
i ., /\ / \ / \
],, . / N/ \ / \
g,, x'.\ / A/" A \
" ,, NNN / r "N/ \\ /
, \. Y NV Po 87 M M M 91 92 M M M M 97 Year
-+-Indicator -G-- Control h0DC Table 4.5-1 Average Annual Cs-137 Concentration in Vegetation Year Indicator Control (pCi/kg-wet) (pCi/kg-wet)
Pre-op 54.6 43.7 1987 24.4 61.5 1988 38.7 0.0 1989 9.7 0.0 1990 30.0 102.0 1991 35.3 62.4 1992 38.I 144.0 1993 46.4 34.1 1994 20.7 57.4 1995 57.8 179.0 1996 0.0 0.0 1997 0 32.6 l
4-17
4.6 River Water Surface water from the Savannah River is obtained at three locations using automatic samplers. Small quantities are drawn at intervals not exceeding a few hours. The samples drawn are collected monthly; quarterly composites are produced from the monthly collections.
The collection points consist of a control location (Station 82) which is located about 0.4 miles upriver of the plant intake structure, an indicator location (Station
- 83) which is located about 0.4 miles downriver of the plant discharge stmeture, and a special location (Station 84) which is located approximately 1.3 miles downriver of the plant discharge stmeture. A statistically significant increase in the concentrations found in samples collected at the indicator station compared to those collected at the control station could be indicative of plant releases.
Concentrations found at the special station are more likely to represent the activity in the river as a whole which might include plant releases combined with those from other sources along the river.
A gamma isotopic analysis is conducted on each monthly sampic. As in all -
previous years,11ere were no gamma emitting radionuclides ofinterest detected in l the 1997 river water samples.
A tritium analysis is performed on each quarterly composite. As indicated in Table 3-1, the average concentration found at the indicator station was 1293 pCi/l greater than that found at the control station. However, this difference was not statistically discemible since it was less than the calculated MDD of 1560 pCi/1. On this basis, the increase is not necessarily attributed to plant releases. At the special station, the results ranged from 393 pCi/l to 1110 pCi/l with an average of 686 pCi/1. The MDC for tritium in river water is 3000 pCi/l and the RL is 30,000 pCi/1.
The historical trending of the average tritium concentrations found at the special, indicator and control stations along with the MDC for tritium is alotted on Figure 4.6-1. The data for the plot is listed in Table 4.6-1. Also, incluc ed in the table is data from the calculated difference between the indicator and control stations; the MDD between the indicator and control stations; and the total liquid releases of l tritium from the plant.
There does not appear to be any good correlation between the plant tritium releases and the differential amount found in the river between the indicator and control stations. The average concentration at the indicator station and its increase over that at the control station for 1997 are higher than in any previous year of operation, although the increase between the two stations remains less than the MDD.
In the fir,t two years of operation, the tritium concentration at the special station was somewhat greater than that at the indicator station. Whereas in recent years, the level at the special station has generally become less than the level at the indicator station. Due to the locations of the indicator and special stations in relation to the p' ant site and other tritium sources, this could be interpreted as an indication that contributions from other tritium sources have diminished, while plant releases have become a larger percentage of the total source.
l 4-18
The annual downriver survey of the Savannah River showed that river water is not being used for purposes of drinking or irrigation for at least 100 miles downriver (discussed in Section 4.1).
1 I
4-19 j
Figure 4.6-1 Average Annual H-3 Concentration in River Water !
3000 2500 i
j1500 \ J '
1000 l
,,, % [ _ /OM/ N ..
I
- l l Po 87 88 89 90 91 92 93 94 95 96 97 l Year l
)
+ Indicator -e- Control -*-- Special MDC l
i Table 4.6-1 l
Average Annual H-3 Concentration in River Water >
1 l
MDD Year Special Indicator Control Difference Annual Site (pCi/l) (pCi/I) (pCill) Between (pCi/l) Tritium Indicator and Released Control (Cl)
(pCi/l)
Pre-op 1900 65 0 665 -15 145 NA i 1987 1411 680 524 156 416 321 1988 1430 843 427 416 271 390 1989 1268 1293 538 755 518 918 1990 1081 1142 392 750 766 1172 1991 1298 1299 828 471 626 1094 1992 929 1064 371 693 714 1481 1993 616 712 238 474 1526 761 1994 774 1258 257 1001 2009 1052 1995 699 597 236 361 766 968 1996 719 1187 387 800 2147 1637 1997 686 1547 254 1293 1566 1449 4-20
1 l
l 4.7 Drinking Water Samples are collected at a control location (Station 80 - the Augusta Water Treatment Plant in Augusta, Georgia located about 56 miles upriver), and at two indicator locations (Station 87 - the Beaufort-Jasper County Water Treatment Plant near Beaufort, South Carolina,112 miles downriver; and Station 88 - the Cherokee Hill Water Treatment Plant near Port Wentworth, Georgia,122 miles downriver).
These upriver and downriver distances in river miles are the distances from the plant to the point on the river where water is diverted to the intake for each of these water treatment plants.
River water samples are taken near the intake of each water treatment plant (raw drinking water) using automatic samplers which take periodical small aliquots from the stream. These composite samples are collected monthly along with a grab sample of the processed water coming from the treatment plants (finished drinking water). Quarterly composites are made from these monthly collections for both raw and processed river water. Gross beta and gamma isotopic analyses are performed on each of the monthly samples while tritium analysis is conducted on the quarterly composites. Although an I-131 analysis is not required to be conducted on these samples, since the dose calculated from the consumption of water is less than 1 mrem per year (see ODCM Table 4-1), an I-131 analysis is !
conducted on each of the monthly finished water grab samples, since a drinkmg l water pathway exists, l Provided in Figures 4.7-1 & 2 and Tables 4.7-1 & 2, are the historical trends of the !
average gross beta concentrations found in the monthly collections of raw and I finished drinking water.
No trend is recognized in the data presented in these graphs and tables. A discernible difference between the gross beta analysis results in drinking water for the two station groups occurred only in raw dnnking water during preoperation and in 1995. The MDC for gross beta in water is 4 pCi/1.
i 1
l I
4-21 l
Figure 4.7-1 ,
Average Monthly Gross Beta Concentration in Raw Drinking l Water i 8
7
^
56 S' )( '
l / \ /V \
l 1 / N. .. _ sk/N.\ l
, -v ~
0 1
0 Po 87 86 89 90 91 92 93 94 95 96 97 Year
-*-Indicator --S- Control MDC i
Table 4.7-1 Average Monthly Gross Beta Concentration in Raw Drinking Water .
Period Indicator (pCi/l)
Control (pCi/l)
) ;
Pre-op 2.70 1.90 1987 2.20 5.50 _
1988 2.67 3.04 1989 2.93 3.05 1990 2.53 2.55 l 1991 2.83 3.08 !
l992 2.73 2.70 {
1993 3.I7 2.83 ;
1994 3.51 3.47 I995 3.06 4.90 1996 5.83 3.02 l 1997 2.93 2.94 l
4-22 i
I Figure 4.7-2 ;
I Average Monthly Gross Beta Concentration in Finished Drinking Water 4
3.5 j
$' 3 l 2.5
.5 , hM "
\ m m dF DO( l
[ l H
h1 0
0.5 0
Po 87 86 89 90 91 92 93 94 95 90 97 Year
-*-Indicator -G- Control MDC Table 4.7-2 l Average Monthly Gross Beta Concentration in Finished Drinking Water Period Indicator Control (pci/l) (pci/I)
~
Pre-op i 2.90 1.80 1987 2.10 1.80 1988 2.28 2.35 1989 2.36 2.38 1990 2.08 1.92 1991 1.90 1.53 1992 2.09 1.67 1993 2.23 2.30 1994 2.40 2.68 1995 2.74 2.32 1996 2.19 2.21 19L/ 2.38 1.77 4-23 l
As provided in Table 3-1, there were no positive results during 1997 for the radionuclih: of interest from the gamma isotopic analysis of the monthly collections tor both raw and finished drinking water. Only one positive result has been found since operation began. Be-7 was found at a concentration of 68.2 pCi/l i in the sample collected for September 1987 at Station 87. Dur~mg preoperation Be-7 was found in about 5% of the samples at concentrations rangmg from 50 to 80 pCi/1. The MDC assigned for Be-7 in water is 124 pCi/1. Also during preoperation, Cs-134 and Cs-137 were detected in about 7% of the samples at <
concentrations on the order of their MDCs which are 15 and 18 pCi/1, respectively.
As shown in Table 3-1, I-131 may have been detected at a concentration of 0.541 pCi/l with an uncertainty of 0.565 pCi/l in the finished drinking water sample collected on May 5,1997 at Port Wentworth. This is the first occurrence for detecting I-131 in finished drinking ' vater since operation began. During preoperation, it was detected in only one of 73 samples at a concentration of 0.77 pCi/l at Port Wentworih. The MDC and RL for I-131 in drinking water are 1 and 2 )
pCi/1, respectively.
Figures 4.7-3 & 4 and Tables 4.7-3 & 4 provide historical trending f >r the average tritium concentrations found in the quarterly composites of raw and finished drinking water collected at the indicator and control stations. The tables also list the calculated differences between the indicator and control stations, and list the MDDs between these two station groups; The average conceptrations at the indicator stations for 1991 and 1992 have been adjusted to remove the impact of the inadvertent release from SRS of 7500 Ci of tritium to the Savannah River about 10 miles downriver of VEGP, in December 1991. The graphs and tables show that in recent years, the tritium concentrations in the drinking water samples, both raw and finished, have been gradually trending downward since 1988. The 1997 raw drinking water indicator station tritium was approximately 42% of that found in preoperation samples and the first three years of operation. The finished drinking water indicator station tritium was approximately 31% of that found in preoperation and the first three years of operation.
4-24
Figure 4.7-3 .
l Average Annual H-3 Concentration in Raw Drinking Water 1
2500 -
N g 1
%_=
1500
\
l-O u - ~
500 l' , ,
O Po 87 88 89 90 91 92 93 94 95 96 97 Year l--+-indicator -G-Control MDCl Table 4.7-3 i i
Average Annual H-3 Concentration in Raw Drinking Water l Period Indicator Control DMerence MDD (pci/l) (pci/I) Between (pci/l)
Indicator and Control j (pCi/l)
Pre-op 2300 400 1900 1987 2229 316 1913 793 1988 2630 240 2390 $80 1989 2508 259 2249 1000 1990 1320 266 1054 572 1991 1626 165 1461 834 1992 1373 179 1194 353 1993 955 0 955 NA l 1994 871 0 871 NA i I
1995 917 201 716 NA 1996 1014 207 807 151 !
1997 956 230 _E 726 61 4 25 <
i
j Figure 4.7-4 l
Average Annual H-3 Concentration in Finished Drinking Water 3000
_ N /\ V e
v,.2=a
( l l 70 l l
j1500 I
\
l 1000
~ 1 1 % . ,
f . ; ;; H I I
Po 87 88 89 90 91 92 93 94 95 96 97 Year j -+-indicator -a- control moc l Table 4.7-4 Average Annual H-3 Concentration in Finished Drinking Water Period Indicator Control Difference MDD (pCi/l) (pCi/l) Between (pCi/l)
Indicator and l Control l (pCi/l)
Pre-op 2900 380 2520 1987 2406 305 2101 1(X)7 1988 2900 270 2630 830 1989 2236 259 1977 627
! 1990 1299 404 895 1131 1991 1471 225 1246 647 1992 1195 211 984 427 L
~~
1993 993 0 993 NA 1994 880 131 749 270 1995 847 279 568 NA 1996 884 168 716 NA 1997 887 221 666 383 t
l 4 26
1 4.8 Fish Table 2-1 calls for the collection of at least one sample of any anadromous species of fish in the vicinity of the plant discharge during the spring spawning season, and for the semiannual collection of at least one sample of any commercially or y recreationally important species in the vicinity of the plant discharge area and in an area not influenced by plant discharges. Table 2-1 specifies that a gamma isotopic analysis be performed on the edible portions of each sample collected.
l As stated in Table 2-2 a 5 mile stretch of the river is generally needed to obtain adequate fish samples. For the semiannual collections, the control location l
(Station 81) extends from approximately 2 to 7 miles upriver of the plant intake i structure and the indicator location (Station 85) extends from about 1.4 to 7 miles downriver of the plant discharge structure. For anadromous species, all collection points can be considered as indicator stations.
l l
American shad was collected as the anadromous species on March 24,1997. As in l all but two previous years of operation, no radionuclides were detected in 1997
, from the gamma isotopic analysis of the anadromous species during the spring l spawning season. In 1987, as well as in 1991, Cs-137 was found in a single
! sample of American shad at concentrations of 10 and 12 pCi/kg-wet, respectively.
The dates and compositions of the semiannual catches at the indicator and control !
stations during 1997 are shown below. i I
I Date Indicator Control !
! April 10 & 14 Channel Catfish Largemouth Bass Largemouth Bass Redear Sunfish October 14 Redear Sunfish Redear Sunfish White Catfish Largemouth Bass l
As indicated in Table 3-1, Cs-137 was the only radionuclide found in the
! semiannual collections of a commercially or recreationally imix>rtant species of l
fish. It has been found in all but 2 of the 85 samples collected during operation and in all but 5 of the 32 samples collected during preoperation. As provided in Table 3-1, the average concentration . ' e indicator station was 46.2 pCi/kg-wet i greater than that at the control station. This difference is not statistically l discemible, as it is less than the calculated MDD of 203.2 pCi/kg-wet. A ('
discernible difference has not occurred for any year of operation or during preoperation.
Figure 4.8-1 and Table 4.8-1 provide the historical trending of the average concentrations of Cs-137 in units of pCi/kg-wet found in fish samples at the indicator and control stations. No trend is recognized in this data. The MDC and RL for Cs-137 in fish are 150 and 2000 pCi/kg-wet, respectively.
4-27
l Figure 4.8-1 Average Annual Cs-137 Concentration in Fish
= ,,
_ \
p ..
1 1
.i" k /"\
! /N , ..
i \ \ / \/ /h //\\
\ el" t \- d /\ y -
/ V. \", ,
y .
0 Po 87 88 W 90 g 92 93 94 95 96 97
--+-- Indicator --S- Control MDC Table 4.8-1 Average Annual Cs-137 Concentration in Fish Year Indicator Control (pCi/ka-wet) (pCi/ka-wet)
Pre-op 590 340 1987 337 119 1988 66 116 1989 117 125 1990 103 249 1991 105 211 1992 178 80 1993 360 84 1994 165 200 1995 125 96 ~
1996 194 ~
404 1997 93 l 139 4-28
l The only other radionuclide found in fish samples during operation is I-131. In 1989, it was found in one sample at the indicator s'ation at a concentration of 18 pCi/kg-wet. In 1990, it was found in one sample, at both the indicator and control stations, at concentrations of 13 and 12 pCi/kg-wet, respectively. The MDC assigned to I-131 in fish is 53 pCi/kg-wet.
During preoperation, Cs-134 was found in two of the 17 samples collected at the control station at concentrations of 23 and 190 pCi/kg-wet. The MDC and RL for l
Cs-134 are 130 and 1000 pCi/kg wet, respectively. Nb-95 was also found in one l of the control station samples at a concentration of 34 pCi/kg-wet. The assigned l MDC and calculated RL are 50 and 70,000 pCi/kg-wet, respectively.
l l
i 1
I I
4-29
i 4.9 Sediment Sediment was collected along the shoreline of the Savannah River on April 8 and I
October 7,1997 at Stations 81 and 83. Station 81 is a control station located about 2.5 miles upriver of the plant intake structure while Station 83 is an indicator l l station located about 0.6 miles downriver of the plant discharge structure. A i gamma isotopic analysis was performed on each sample. l
! The historical average concentrations of Be-7, Co-58, Co-60, and Cs-137 in i sediment are plotted in Figures 4.9-1 through 4.9-4 along with listings of their l concentrations in Tables 4.9-1 through 4.9-4. The concentrations of the solely man-made nuclides (Co-58, Co-60, & Cs-137) dropped significantly at the indicator station in 1997 compared to the previous several years. Be-7, produced by man and nature, also dropped significantly at the indicator station, but rose at the control station.
During preoperation, Zr-95, Nb-95, Cs-134, and Ce-141 were detected in at least one of the control station samples and Nb-95 was detected in one of the indicator station samples. Be-7 and Cs-137 were found in several of the samples. The concentrations of these nuclides were on the order of their respective MDC values.
The presence of these preoperational nuclides could be attributed to atmospheric weapons testing and the Chernobyl accident.
Mn-54 and I-131 were found sporadically over several yea s of operation. A sununary of the positive results for these nuclides along with their applicable MDC's is provided in Table 4.9-5.
For Be-7, the average level at the indicator station during 1997 was 102 pCi/kg-dry greater than that at the control station; however, this difference is not statistically discernible since it is less than the calculated MDD of 3465 pCi/kg-dry. There continues to be no statistically discernible difference between the indicator and control stations for Be-7 and on this basis its presence at the indicator station is not attributed to plant releases.
For Cs-137, the average concentration at the indicator station during 1997 was 86 pCi/kg-dry greater than that at the control station. This difference is statistically discernible since it is greater than the MDD. This is the second occasion during operation that a discernible difference was found. The first time occurred in 1996.
The Cs-137 level at the indicator station has averaged nearly 150 pCi/kg-dry greater than that at the control station over the entire period of operation. During preoperation, the Cs-137 was 170 pCi/kg-dry greater at the indicator station than at the control station.
Co-60 was found in the two indicator station samples, but was absent from the control station samples and thus no MDD could be calculated for it.
The higher concentrations of Cs-137 and Co-60 at the indicator station over those at the control station are indicative of plant releases. The annual whole body dose l
' to an individual from direct radiation from sediment containing the reported concentrations of these radionuclides found at the indicator station minus those found at the control station was estimated (employing the methodology and parameters of NRC Regulatory Guide 1.109, Revision 1, October 1977) to be approximotely 2.62 micrcrem or about 0.09% of the 3 mrem limit, for liquid releases from one unit as specified by ODCM 2.1.3. This dose, although calculable, is insignificant with respect to regulatory limits.
1 4-30 l
Figure 4.9-1 l
Average Annual Be-7 Concentration in Sediment
=
2soo 32000 g Is- A ,\
\ /
7 3i n-1 7 , xv ; y v 4 - s -
0 ,,, '
Y ' M ;(
l l
o Po 87 88 09 90 91 92 93 M 95 96 97 Year
( -+- indicator -G-- Control RADC l
1
! Table 4.9-1 i
Average Annual Be-7 Concentration in Sediment MDC=656 pCi/kg-day l
l Year Indicator ' Control (pCi/kg-dry) (pCi/kg-dry)
Pre-op 580 500 1987 987 543 l 1988 970 810 1989 1300 415 1990 465 545 1991 826 427 1992 2038 380 1993 711 902 1994 1203 964 1995 1865 1575 1996 1925 831 _
1997 1130 1028 4-31
l l
Figure 4.9-2 Average Annual Co-58 Concentration in Sediment n
g.
- a. /\
x 8-
/\ . , ,
/ \
/ \ ^ \
~
1 J,. . / \ / \ \
, 1 9,
\/
92
\/
93 94 96 96
\
97 Po 87 88 89 91 Year
--+-- Indicator -e-- Control MDC Table 4.9-2 Average Annual Co-58 Concentration in Sediment ,
MDC=43 pCi/kg-dry Year Indicator Control (pCi/kg-dry) (pCi/kg-dry)
Pmep 0 0 1987 0 0 1988 190 0 1989 135 0 1990 140 0 1991 0 0 1992 124 0 1993 0 0 1994 18.4 0 1995 42.4 0 1996 274 0 1997 0 0 i
4-32 j
i l
1 Figure 4.9-3 j i
l Average Annual Co-60 Concentration in Sediment j 350 m
?.- / \ 4 s
[ \'
12a I
.li / \
g 150 1
/
x s
/ \c s r i
O J / \W i 50 0:
(
l Po 87 88 80 90 91 92 93 94 96 94 97 l
Year
-+-Indicator --S- Control RADC i
i Table 4.9-3 j Average Annual Co-60 Concentration in Sediment 1
MDC=70 pCi/kg-dry l
, Year indicator Control i l (pCl/ka-dry) (pCi/ka-dry) :
Pre-op 0 0 l 1
1987 0 0 )
62 0 j l 1988 1989 46 0 l 1990 46 0 1991 113 0 l 1992 59.5 0 l l 1993 65.9 0 ,
1994 85.2 0 l
- 995 267 0
1996 344 0 l 1997 86 0 i l
i 4-33 ,
i t
Figure 4.9-4 4 l
l Average Annual Cs-137 Concentration in Sediment a00
_ 500 I
g- ;
1,, s A /
I-
^ / - / V l ,,, ~../ ~ / .
FN 100 ..
0- l Po 87 88 09 90 91 92 93 94 96 96 97 Year
-*-Indicator -e- Control MDC 1
l Table 4.9-4 Average Annual Cs-137 Concentration in Sediment i
MDC-180 pCi/kg l
l Year Indicator Control ,
(pCi/kg) (pCi/kg) l Pre-op 320 150 1987 209 111 l 1988 175 175 1989 230 125 1990 155 140 1 1991 246 100 l 1992 259 111 1993 345 115 1994 240 118 1995 357 123 1996 541 93 1997 184 98 4-34 l
l Table 4.9-5 Additional Sediment Nuclide Concentrations Nuclide YEAR Indicator Control MDC (pCi/kg-dry) (pCi/kg-dry) (pCi/kg-dry)
Mn-54 1988 22 0 1989 18 0 42 1994 32 0 1-131 1992 194 20 53 1994 51 41 l
i l
i 4-35 l 1
i r
l 5.0 INTERLABORATORY COMPARISON PROGRAM i l
l requirements of Regulatory Guide 4.15, Revision 1, " Quality Assurance for l Radiological Monitoring Programs (Normal Operations) - Efiluent Streams and the Environment", February 1979. The guide indicates that the ICP is to be conducted l with the EPA's (Environmental Protection Agency) Environmental Radioactivity
, Laboratory Intercomparison Studies (Cross-check) Program or an equivalent l program, and that the ICP should include all of the determinations (sample medium /radionuclide combinations) that are offered by the EPA and included in I the REMP. l The ICP is conducted by Analytics, Inc. of Atlanta, Georgia. Analytics has a j documented Quality Assurance program and the capability to prepare Quality l Control materials traceable to the National Institute of Standards and Technology.
The ICP is a third party blind testing program which provides a_means to ensure independent checks are performed on the accuracy and precision of the ,
measurements of radioactive materials in environmental sample matrices. I Analytics supplies the cross check samples to the EL which ?erforms the laboratory analyses in a normal manner. Each of the specifiec analyses is l performed three times. The results are then sent to Analytics who performs an I evaluation which may be helpful to the EL in the identification ofinstrument or procedural problems.
The accuracy of each result is measured by the normalized deviation which is the ratio of the reported average less the known value to the total error. The total error is the square root of the sum of the squares of the uncertainties of the known value and of the reported average. The uncertainty of the known value includes all analytical uncertainties (counting statistics, calibration uncertainties, chemical yield etc.). The uncertainty of the reported average is the standard deviation of the analysis results performed by the EL. The precision of each result is measured by the coefficient of variation which is defined as the standard deviation divided by the reported average. An investigation is undertaken whenever the absolute value i of the normalized deviation is greater than 3 or whenever the coefficient of I variation is greater than 15%. i As required by ODCM 4.1.3.3 and 7.1.2.3, a summary of the results of the EL's participation in the ICP is provided in Table 5-1 for: the gross beta analysis of an air filter and of 3 water samples; the gamma isotopic analysis of an air filter, a milk ,
sample, and 2 water samples; and the tritium analysis of 2 water samples. l Delineated in this table for each of the media / analysis combinations are: the specific radionuclides; Analytics' preparation dates; the known values with their uncertainties supplied by Analytics; the reported averages with their standard deviations; and the resultant normalized deviations and coefficients of variation l expressed as a percentage. It may be seen from Table 5-1 that each of the results l satisfied the acceptance criteria for the coefficient of variation, but 6 of the 44 results exceeded the acceptance criteria for normalized deviation. The outcomes of investigations into these 6 results are provided in subsequent paragraphs.
The Cs-134 gamma analysis results in the December 11 air filter and in the March 20 water sample were both low compared to their "known values". The two l
primary gamma decay peaks at 604 and 795 kev cause a coincidence peak at 1399 l
5-1 1
L
kev (the sum of the two primary peaks). A correction factor for this summing effect will be applied to future results.
The Ce-141 gamma analysis results, from the same two samples, were also low compared to their "known values". The gamma decay peak for Ce-141 is 145 kev. The presence of the 144 kev gamma from Fe-59 may affect the background calculation for Ce-141 causing low values. Future analyses will extrapolate the background for the Ce-141 peak to account for the interference of the 144 kev peak. This should bring the results within the acceptable limit.
For the gross beta results in the March 20 water sample, a gamma scan was used to confirm the high activity for the standard used to determine gross beta efficiency.
When the proper standard was used, the normalized deviation was within the acceptable limit.
For the gamma analysis for I-131 in the September 18 water sample, the c ucstionable result was due to an electronic problem regarding pole zero in one of tae detectors. The electronics have been recalibrated to reduce variation.
The results of these investigations have been used to identify interferences an[
instrument deficiencies which have been or are being corrected to prevent reoccurrence.
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6.0 CONCLUSION
S This report confimis the licensee's conformance with the requirements of Chapter )
4 of the ODCM during 1997. It provides summaries of data collection activities I and a discussion of the results of the laboratory analyses for the samples.
Co-60 and Cs-137 (the differential amount between the indicator and control stations) in shoreline sediment downriver, in close proximity to the discharge structure, are indicative of plant releases. The consequent dose is a trivial fraction of the ODCM limits and poses no measurable radiological impact to the environment or the public.
No discemib'.e radiological impact upon the environment or the public as a consequence, of plant discharges to the atmosphere and to the river was established for any other REMP samples. ,
1 l
I i
6-1
,