ML20140G645

Evaluation of Radioactive Liquid Effluent Releases from Rancho Seco Nuclear Power Plant

ML20140G645
Person / Time
Site:	Rancho Seco
Issue date:	03/31/1986
From:	Cottrell W, Loar J, Chris Miller, Witherspoon J OAK RIDGE NATIONAL LABORATORY
To:	Office of Nuclear Reactor Regulation
References
CON-FIN-A-9468 NUREG-CR-4286, ORNL-TM-6183, TAC-56033, NUDOCS 8604030073
Download: ML20140G645 (108)

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NUREG/CR-4286 ORNL-6183

Evaluation of Radioactive Liquid Effluent Releases From the Rancho Seco Nuclear Power Plant  !

Prepared by C. W. Miller, W. D. Cottrell, J. M. Loar, J. P. Witherspoon Oak Ridge National Laboratory Prepared for U.S. Nuclear Regulatory l Commission l

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NOTICE This report was prepared as an account of work sponsored by an agency of the United States Government. Neither the United States Government not any agency thereof, or any of their employees, makes any warranty, expressed or implied, or assumes any legal liability of re-sponsibility for any third party's use, or the results of such use, of any information, apparatus, product or process disclosed in this report, or represents that its use by such third party would not infringe privately owned rights.

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l NUREG/CR-4286 ORNL-6183 Evaluation of Radioactive Liquid Effluent Releases From the Rancho Seco Nuclear Power Plant Manuscript Completed: December 1985 Date Published: March 1986 Prepared by C. W. Miller, W. D. Cottrell, J. M. Loar, J. P. Witherspoon NRC Project Manager: M. E. Wangler Oak Ridge National Laboratory Oak Ridge, TN 37831 Prepared for Division of Pressurized Water Reactor Licensing-B Office of Nuclear Ret.ctor Regulation U.S. Nuclear Regulatory Commission Washington, D.C. 20555 NRC FIN A9468

ColmWIS Pnne vil LIST OF FIGURES . .... . . . . ... ... . .. . . . . . . . . .. . . . .

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- LIST OF TABLES . . .... . . . .. .. ... . . . . . . . . . . . . . . . . .

zi AGNOWLEDGMEhTS . .... . .. . ... .. . . . . . . . . .. . . . . . . . .

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[AB5 TRACT . . ... ... . . ..... . . .. . . . . . . . . . ... . .. .

EXECUTIVE RMIARY . . .. . . . . .. . . . . . . . . . . . . . . . . . . . . . xv 1

1. INTRODUCTION .. . . . . . . .. .. .. . . . . . . . . . . . . . . . . . .

. . .. . . . . . . . . .. . . . . . . . . 5

2. SURVEY METHODS AND PROCEDURES .

5 2.1 MEASUREMENT OF EITERNAL GAMMA RADIATION LEVELS . . .. . . . . . . . .

5 2.2 SOIL AND VEGETATION SAMPLING . . . . . . . . . . . ... . . . . . . .

7 2.3 SILT AND WATER SAMPLING , . .. . . . . . . . . . . . . . . . . . . .

FISH, FROGS, AND GAME BIRDS . . . . . . . . . . . .. . . . . . 7 2.4 . . .

8 2.4.1 FISH . . . . . . .. . . . . . . . . . . . . . . . . . . . . .

11 2.4.2 FROGS . . . . . . . . . . . . . . . . . . . . . . . . . . . . .

11 2.4.3 GAME BIRDS . . .. . . . . . . . . . . . . . . . . .. . . . .

. . . ... . . . . . . . . . . . .. . . . . 13

3. ENVIRONMENTAL SURVEY RESULTS

. . . . . . . . . . . . . . . . . 13 3.1 TFREFSTRIAL BACKGROUND MEASUREMENTS

. . . . . . . . . . . . . . . . . . . 13 3.2 EITERNAL GAMMA RADIATION LEVELS 14 3.3 SOIL SAMPLING . . . . . . . . . . . . . . . . . . . . . . . . . . . .

14 3.4 VEGETATION SAMPLING . . . .. . . .. . . . . . . . . . . . . . . . .

22 3.5 SILT SAMPLING . . . . . . . . . . . . . . . . . . . . . . . . . . . .

22 3.6 WATER SAMPLING . . . . . . . . . . . . . . . . . . . . . . . . . . .

3.7 BEEF SAMPLING . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24 3.8 BONEY SAMPLING . . . . . .. . . . . . . . . . . . . . . . . . . . . . 24 3.9 FISH, FROGS, AND GAME BIRDS . . . .. . . . . . . . . . . . . . . . . 24 3.9.1 FISH . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 26 3.9.2 FROGS . . .. . . . . . . . . . . .. . . . . . . . . . . . . . 33 3.9.3 GAME BIRDS . . . . . . . . . . . . . . . . .. . . . . . . . . 34

4. RADIATION DOSE ASSESSMENT . .. . . . . . . . . . . . . . . . . . . . . . . 37 4.1 PNIlfWAYS OF INTERNAL EXPOSURE . . . . . . . . . . . . . . . . . . . . 37 4.1.1 INGESTION . . . . . . . . . . . . . . . . . . . . . . . . . . 38 4.1.2 INHALATION . . . .. . . . . . . . . . . . . . . . . . . . . . 44 4.2 PA'IIIWAYS OF EITERNAL EXPOSURE . . . . . . . . . . . . . . . . . . . . 45 4.3 ALTERNATE DOSE CONVERSION FACTORS . . . . . . . . . . . . . . . . . . 46

5. INVENTORY OF RADIONUaIDES IN IRRIGATED FIELDS . . . . . . . . . . . . . . 47

6.

SUMMARY

OF RESULTS . . . . . . . . . . . . . . . . . . .. . . . . . . . . 51

7. REFERENCES . . . . . . . . ... . . . . . . . . . . . . . . . . . . . . . 55 j

x (X)NCENTRATION OF RADIONUaIDES IN ENVIRONENTAL SAMPLES . . . . . 57 APPENDII A.

QUALITY CONTROL PROGDURES . . . . . . . . . . . . . . . . . . . 75 APPENDIX B.

HRI EASE DATA . . .... . . . . . . . . . . . . . . . . . . . . . 93 APPENDII C.

ADDITIONAL PARTICIPANTS IN HIS PROJECT . . . . . . . . . . . . . 97 APPENDIX D.

APPENDIX E. RADIATION UNITS USED IN H IS REPORT . . . . . . . . . . . . ... . 101 l

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I LIST OF FIGURES Flaure Pane 1 The Rancho Seco Nuclear Power Plant (RSNPP) and its environs . . 2 2 Schematic of the Rancho Seco Nuclear Power Plant environs showing the division of irrigated land into units (fields) for sampling Purposes . . . . . . . . . . . . . . . . . . . . . . 6 3 Sampling locations in Field 14 (Sacramento Municipal Utility District property), showing overflow of Clay Creek into field . . 15 4 Sampling locations in irrigated fields along Clay Creek immediately downstream from Sacramento Municipal Utility District . . . . . . . . . . ......... . . . . . . . . . 16 5 Sampling locations in irrigated fleids along Clay Creek near California Highway 104 . . . .. . . . . . . . . . . . . . . . . 17 6 Sampling locations in Field 9, Clay Creek, and California Highway 104 . . . . . . . . . .. . . . . . . . . . . . . . . . . 18 7 Sampling locations in irrigated fields at the confluence of Clay and Hadselville Creeks . . . . . . . . . . . . . . . . . . . 19 8 Plat map showing Rancho Seco Nuclear Power Plant and streams receiving liquid wastes from plant. Water and silt sampling locations are indicated on map . . . . . . . . . . . . . . . . . . 20 9 Typical irrigated field showing division into sections for use in arriving at weighted average radionuclide concentration . . 48 A-1 California background sampling locations . . . . . . . . . . . . . 59 i

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I LIFT OF TABLES Table fast

1. Location and description of fish sampling sites in streams and ponds near the Rancho Seco Nuclear Power Plant . . . ....... 9

2. Average concentrations of cesina in soil, vegetation. and silt . . 21

3. Concentrations of I37 Cs and 134 Cs in silt from Clay, Hadselville, and Laguna Creek . . . .. . . . . .... . . . . . ....... 23

4. Concentration of radionuclides in beef samples from Rancho Seco Nuclear Power Plant environs. . . . . . . . . . ....... 25

5. Mean concentration (pC1/3. wet vt.) of radionuclides in axial muscle of fish collected from streams downstream of The Rancho Seco Nuclear Power Plant, December 1984. . . . . . . . . . . . . . 27

6. Mean concentration (pC1/3. wet vt.) of radionuclides in axial muscle of fish collected from small ponds near The Rancho Seco Nuclear Power Plant, November / December 1984. . . . . . . . . . . . 28

7. Percentage of'the fish analyzed for radionuclides that exceeded the minimum quality length proposed by Gabelhouse (1984) . . . . . 30

8. Radiation doses from ingestion of fish caught in the vicinity of Rancho Seco . . . . . . ... . . . . . . . . . . . . 39

9. Radiation doses from ingestion of frogs and game birds caught in the vicinity of Rancho Seco . . . . . . . . . . . . . . 41

10. Radiation doses from ingestion of beef . . . . . . . . . . . . . . 43

11. Cesium inventory in fields, samp, and ponds 1 and 2 . . . . . . . 50

12. Dose to a hypothetical individual from past liquid effluents from Rancho Seco . ........................ 52 A-1 Concentrations of radionuclides in California backgroand soll samples . . . ........................ 60 A-2 Concentrations of radionuclides in soll samples . . . ...... . 61 A-3 Concentrations of radionuclides in vegetation samples . . . . . . . 64 A-4 Concentrations of radionuclides in sitt samples . . . . . . . . . . 66 A-5 Concentrations of radionuclides in water samples . . ... . . . . 67 A-6 Concentration of radionuclides in exist muscle of fish collected at various sites downstream of the Rancho Seco Nuclear Power Plant . . . . . . . . .. . . . . . . . ... . . . . 68 As

4 A-7 Concentration of radionuclides in axial muscle of fish collected from three small ponds near the Rancho Seco

. 70 Nuclear Power Plant . . . . . . . . . . . . . . . . . . . . . . .

A-8 Concentration of radionuclides in axial muscle of frogs

. . . . . . 72 from two sites near the Rancho Seco Nuclear Power Plant A-9 Concentration of radionuclides in axial muscle of game birds collected at several sites near the Rancho Seco . 73 Nuclear Power Plant . . . . . . . . . . . . . . . . . . . . . . .

B-1 Comparison of gamma spectrometry resnits of soil sample . 78 analyses performed by two independent laboratories . . . . . . .

B-2 Comparison of radionuclide concentrations in duplicate tissue 79 samples analyzed with NaI and GeLi detectors . . . . . . . . . . .

C-1 Liquid effluent releases (Ci) from the Rancho Seco Nuclear . 95 Power Plant . . . . . . . . . . . . . . . . . . . . . . . . . . .

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ACINOWLEDGMEhTS We would like to thank our NRC Project Manager, Michael E. Wangler, for his many helpful comments and suggestions during the course of this proj ect. We are grateful to S. E. Hucksba, S. Whit e, S. R. Morris, and U. F. Strong for their untiring help in producing this report. We also thank B. G. Blaylock, K. F. Eckerman, C. T. Garten, D. C. Kocher, and A. S. Qui st for their aid in reviewing earlier drafts of this manuscript.

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ABS"IltACT A project has been carried out by Oak Ridge Na tio na l Laboratory (ORNL) to e st ima t e the concentrations of radionuclides in the environment that have resulted from the release of radioactive materials in the liquid waste effluents from the Rancho Seco Nuclear Power Plant (RSNPP) and to estimate possible radiation doses to man resulting from current environmental concentrations. To carry out the objectives of this proj ect, two visits were made to the RSNPP site by scientists from ORNL during Nov embe r and December of 1984 to conduct an environmental sampling program around the site. Elevated levels of same radionuclides were found in the immediate environment of the plant. This radioactive contamination occurs primarily along streams receiving ef fluent from the plant and in fields irrigated with water from these streams. The primary contaminants are 137Cs and 134Cs with lesser amounts of 60Co and 58Co. Specific pathways of exposure and usage factors were not precisely known for the dose assessment of current and potential use of cont am ina t ed water and soil around the RSNPP. The ingestion of fish is the single most important pathway identified in this analysis.

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l EXECUTIVE

SUMMARY

Small leaks in the steam generation system at the Rancho Seco Nuclear Power Plant (RSNPP), located 56 km (35 miles) southeast of Sacramento, California, have led to the release of aqueous radioactive waste materials. Prior to the late summer of 1984, some amounts of radioactivity thus generated were periodically released to the 1

environment. As a result of these releases, members of the general public could potentially be exposed to ionizing radiation. Because of this potential, the U.S. Nuclear Regulatory Commission (NRC) contracted with the Oak Ridge National Laboratory (ORNL) to conduct an evaluation of this radioactive contamination. The objectives of this project were to estimate the concentrations of radionuclides in the environment that have resulted from the RSNPP liquid releases and to estimate current possible radiation doses to man resulting f rom these releases.

To carry out the objectives of this project, two site visits were made to the RSNPP by ORNL scientist s during November and December of 1984 to conduct an environmental sampling program in the vicinity of the site. Elevated levels of some radionuclides were found in the immediate environment of the plant. This radioactive cont amina t ion occurs primarily along streams receiving ef fluent from the plant and in fields irrigated with water from these streams. The highest levels of radionuclides occur immediately below the plant's release point, then decrease with distance from the plant downstream along Clay and

! Hadselville creeks, and approach backt,round levels in Laguna Creek approximately 19 km from the plant. The primary contaminant s are 137Cs i and 134Cs with lesser amounts of 60Co and 58Co.

Higher-than-background levels of radioactivity were detected in

! fish inhabiting the stream that receives liquid effluent from the plant.

Radionuclide concentrations in fish dec11aed with increasing distance down st r e am of the RSNPP. Concentrations in green sunfish from Clay

! Creek at the plant boundary were 200 times background levels of the radionuclides sampled; concentralons decreased by 35% in Hadselville

Creek, approximately 4 km downstream. Concentrations in fish decreased by almost an order of magnitude between the Hadselville Creek and upper Laguna Creek sites, which are an additional 4 km downstream of the xv

release point. The highest cesium concentrations ocentred in largemouth bass collected f rom a snap at the boundary of the RSNPP. At three of five sites, cesium concentrations were higher in piscivorous (e.g.,

largemouth bass) than in nonpiscivorous species.

Specific pathways of exposure and usage f actors were not precisely known for the dose a s se s sment of current and potential use of contaminated water and soll around the RSNPP. The ingestion of fish is the dominant exposure pathway identified in this analysis, my1

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1. INTRODUCTION The Ra ncho Seco Nuclear Power Plant (RSNPP) is located approximately 56 km (35 alles) southeast of Sacramento, California, in Sacr ament o County. Operated by the Sacr ament o Municipal Utility District (SNUD), this pressurized water reactor received its operating license from the U.S. Nuclear Regulatory Commission (NRC) in 1974.

RSNPP was designed to have no liquid radionuclide discharges; however, leaks in the staan-generator system have led to the creation of liquid radioactive waste materials. These wastes, as well as other waste waters generated by the RSNPP, are collected and treated in regenerate holdup tanks. Until late sammer of 1984, the treated waters containing some amount s of radioactive fission and neutron activation products were periodically released to one or two on-site retention basins. The contents of these basins were diluted and subsequently released to Clay Creek. As can be seen in Fig.1, Clay Creek leaves the RSNPP si t e-bounda ry fence approximately 0.5 km from the point of discharge and continues until it joins with Hadselville Creek, which in turn joins with other bodies of water farther downstream. The primary suspected radionuclides released via this pathway were 134 Cs and I37 Cs.

However, small amounts of 38, 14 C, 60Co, and other radionuclides would be expected to be released during normal ope ra ti on s . As a result, selected environmental samples were screened for these radionuclides as well as for 34 Mn, 238g , 903 ,, 238p ,, 239p ,, 244 Am, a nd others (see Appendix C).

Substantial liquid releases of radionuclides to the environment are no longer occurring at the RSNPP. How ev e r , it is evident from Fig. I that members of the general public could potentially be exposed to ionizing radiation as a result of the liquid effluent releases that have already taken place from the RSNPP. Game fish have been caught in unpo st ed areas in the RSNPP environs. Yater taken from Clay Creek, Hadselville Creek, and other streams is used to irrigate pasture lands upou which beef cattle have grazed. Because of these and other potential pathways of exposure, the NRC contracted with Oak Ridge National Laboratory (ORNL) to conduct an independent evaluation of the radioactive contamination from the RSNPP, The objectives of this 1

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3 proj ect were to identify and estimate the concentrations of radionuclides in the environment resulting from the RSNPP liquid releases and to estimate possible current radiation doses to man resulting f rom these releases. The purpose of this report is to document the results of this evaluation for use by NRC.

To carry out the objectives of this report. two visits were made to the RSNPP site by scientists from ORNL. In November 1984, a small group spent approximately one week at the RSNPP obtaining prel imina ry environmental sample s and constructing plans for the later, more detailed survey trip. A second. larger group of ORNL staff spent approximately two weeks in December 1984 at the RSNPP completing the environmental sampling program. This survey included measuring the f ollowing:

1. External samma radiation levels along the stream banks and in fields adjacent to streams that received radioactive effluent from the plant.

2. Concentration of radionuclides in silt and water from streams and ponds that had received potentially contaminated liquid effluent.

3. Concentration of radionuclides in fish, frogs, and birds found in or near the potentially contaminated waterways.

4. Concentration of radionuclides in soil and vegetation from fields irriga ted with water from af fected streams.

5. Concentration of radionuclides in beef from a cow that had reportedly grated on potentially contaminated pasture land. .

6. Concentration of radionuclides in honey.

Section 2 of this report discusses the methods and procedures used to obtain these environmental samples, and Sect. 3 summarises the environmental concentrations that were measured. Section 4 presents the dose assessments that were performed for various potential pathways of

4 exposure based on the resnits of the environmental measurement activity.

Estimates of the radionuclide inventory on irrigated fields are presented in Sect. 5, while Sect. 6 summarises the results of the proj ec t . He appe ndise s provide more detailed results of the environmental sampling program.

It shon1d be noted that current noe of the land sampled in this study is for pasture only. No crops for human consumption are currently grown in these irrigated fields.

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2. SURVEY METRODS AND PROCEDURES 2.1 MEASUREMENT OF EITERNAL GAltlA RADIATION LEVELS Gamma radiation levels were measured along the banks of Clay.

Hadselville. and Lagnas creeks and in fields identified as having been

' irrigated with water from either Clay or Radselville creeks. Gamma scans were performed in the irrigated fields and along the banks of Clay Creek from the RSNPP waste outfall to the confluence of Clay and Hadselville creeks.

All gamma radiation measurements were made using portable scintillation' (NaI) detectors. At selected locations, esternal games radiation levels were measured using both scintillation counters and pressurized ionisation ch ambe r s . The relationship between these comparative measurements was used to convert scintillation counter measurements to dose (esposure) rates.

For convenience la sesaming. the irrigated land was divided into fields (irrigation salts Fig. 2). Each field was scanned using a gamma scintillation detector held approximately 5 ce from the ground surface.

Areas of elevated samma radiation levels were acted, and the maalean level observed was recorded for each area. ,

2.2 SOIL AND VEGETATION SAMPLING Results of the radiation measurements made la the irrigated fields were used as a guide in selecting locations for soll and vegetation samplings. Generally, radkation levels were higher near irrigation pipe outlets and decreased with distance from the outlets la the direction of water flow across the fields. Each field that showed elevated levels of gamma radiation was divided into two or more areas based on the games levels observed. Representative sosples of both soil and vegetation were collected from each area of each fleid. Samples were collected f rom an area 15 se la diameter sad $ cm deep. At selected locations, to evaluate the depth of penetration of the contamination lato the soll, samples were taken at 5-ce latervals from the surface to a depth of 30 ca. A total of 106 soil samples were collected from 80 samplias locationes however, because of resource limitations, only $7 samples were subjected to analyses.

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Emploratory radiochemical analyses were performed on a limited manber of so!!, silt, water, and vegetation samples. Based on the results of these analyses and on reported radionuclides discharged from the plant (Appendix C) together with their respective hasard indices, specific radionuclides were selected for investigation. These radionuclides are given in Appendit A, tables A-1 through A-5.

Samples of soil were dried at 1100C for 24 h and pulverized to a particle size <500 pm (-35 mesh). Aliquot of soil were counted on a Ge(Li) detector, and the spectra were analyzed by computer techniques.

Concentrations of 2380 and 235U in selected samples were determined by neutron-activation methods, and concentrations of alpha- and beta-emitting radionuclides were de t e rm ine d by radiochemical procedures (which are described in the ORNL master analytical chemistry manual).

Samples of vegetation were collected and placed in plastic bass and returned to ORNL for analyses. Vegetation samples were assayed as collected (vet) using techniques analogous to those used in assaying soil.

2.3 SILT AND WATER SAMPLING Silt (sediment) and water samples were collected from Cisy, Hadselville, and Laguna creeks and f rom samps and holding ponds used in the process of transferring water from Cisy and Hadselville creeks to irrigate the pasture fields. Silt samples were dried, pulverized, and analyzed using the esse procedures and methods as were used for soil samples.

Water samples were collected in 1 gal (3.8 L) plastic containers and acidified with nitric acid (10 m1, 70% KNO3/gst) to ministne adsorption of contaminants on container walls. Water sample analyses were performed using standard radiochemical separation and counting techniques (as described in the ORNL master analytical chemistry manual).

2.4 FISH, FROGS, AND GAME BIRDS Because of their potential importance in the diet of several local residents, samples of fish, frogs, and game birds were collected to determine the concentrations of I37Cs, I34Cs, and 60 Co in the flesh.

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1 These radionuclides were selected for analysis because they are routinely released from pressurized water reactors  !!ke that at the RSNPP and were found in a preliminary analysis of fish collected f rom the samp near Clay Creek in November. Because these radionuclides have relatively long half-lives (2 to 30 years), they can contribute a significant portion of the dose to man from fish consumption. No other gamma-ray emit ters were found, either in the preliminary analysis of the November samples or in the analysis of selected sample s collected in December (Appendix B). Water analyses indicated no levels of other radonuclides that would contribute significantly to dose to man from ingestion of fish (Appendia A).

2.4.1 Elih Fish were collected in November and December 1984 at eight sites near the RSNPP (Table 1). Eight fish were collected by angling f rom the small sump adjacent to Clay Creek at the SMUD property line on the initial sampling trip in Nov emb e r. After obtaining a scientific collecting permit from the State of California, Department of Fish and Game, an additional 52 fish were collected by electroshocking during the week of December 9,1984. A Smith-Root Type IV backpack electroffsher with a gasoline-powered generator capable of delivering up to 1200 V of pulsed direct current was used to sample approximately 50 to 150 m of stream, depending upon fish densities at the site. Although the snap adjacent to Clay Creek could be sampled by wading, a small boat was used to sample ponds 1 and 2.

Based on preliminary information indicating that blueg!!!, bass, and catfish constituted the catch of local anglers, we attempted to obtain samples of each group from the eight sites. At many sites, however, only two of three groups were present, and at some sit es (e.g. ,

Clay and Hadselville creeks), bluegill (Lecomis RA112shirus ) were not abundant. Consequently, the green sunfish (LgypAjj syAnglig1) was selected as a target species because (1) it was the dominant (most abundant) sunfish at most sites, and (2) it is large enough to be sought by anglers. Other target spe ci e s included the largemouth bass (Micropterus salmoldes), black bullhead (Ictalurus p1111), and black crappie (Pomonis alsromaculatus), which was found only in Laguna Creek

Table 1. Location and description of fish sampling sites in streams and ponds near the Rancho Seco Nuclear Power Plant Sampling Approximate distance Location 3,,,33, site downstream of date(s), 1984 RSNPP (km)

Clay Creek At SNUD 0.5 December 10,12 property line Nadselville Creek Just above bridge on 4.5 December 12 Clay Station Road Laguna Creek At Laguna Road 9.0 December 11 Lagmas Creek 1.5 km above bridge 15.5 December 12 on McKema le Road w

Dry Creek 200 m below bridge December 12 (control) on Ete. 104 Semp Just morth of Clay Creek 0.5 November 14 at SNED property line December 10, 12 Pond 1 0.5 km SW of SNUD 1.0 December 10 property line Pond 2 Near S!!va feedlots and 6.0 December 11 a dj acen t to Bedselville Creek

" Sampling site located approximately 14 km east of the Rancho Seco Nuclear Power Plast.

C3 at the Laguna Road site. Radionuclide analyses were limited to the three largest individuals of each species at each site. In some cases, one of these species was collected at a site but not analysed because the individuals were judged to be too small to be kept by anglers (e.g.,

largemouth bass in Hadselville Creek and in Laguna Creek at Laguna Road). Finally, an adequate and a representative sampl e was not obtained from Laguna Creek near McKenzie Road. High stream flows and turbid water made electroffshing difficult, and only a few small fish were collected.

Fish collected from each sampling site were placed in plastic bags, stored on dry ice, shipped within 1 to 3 d to DRNL, and stored in a freezer. Prior to sample preparation, each fish was identified to species using the taxonomic keys of Eddy (1969) and Pflieger (1975);

sezed, if possible; measured (total and standard lengths) to the nearest 0.1 ca; and, in most cases, weighed to the nearest 0.1 3 Weights were inadvertently omitted initially; thus, weights of these individuals were estimated from length-weight regressions for each species. To obtain an accurate estimation of weight based on length, the number of fish used in the regression analysis were maximized by including (1) those individuals collected but not analyzed and (2) ladividuals of the same species from different, but similar, sites (e.g., all stream sites, except Dry Creek, were combined).

A 6- to 15-g semple of axial muscle, excluding the skin, was f

r emoved from each fish. The sample was placed in a preveighed 25- by 150-mm glass tube, reveighed, and analyzed for 137Cs, 134C s, and 60Co with a Packard NaI(TI) detector assembly connected to a Canberra Series 35 multichannel analyser. Samples collected on November 14, 1934, were '

analyzed on December 10, and the samples that were collected December 9-13, 1984, were analyzed January 14-17, 1985. Counting timions obtained from the U.S. Env ironment al Protection Agency (EPA)

Environmental Monitoring Systems Laboratory, Las Vegas, Nevada, and used to de t e rmine the counting efficiency for each isotope. The detection limit for all analyses was 0.45 pC1 per sample (1 dpa divided by 2.22 dps/pCl) .

11 2.4.2 Froms Cool temperatures prevented the collection of as adequate semple of frogs. Very few individuals were observed daring daytime surveys along the stream banks and shorelines of the small pond s . Gigging was attempted after smaset in Laguna Creek but was assuccessful. The three individuals that were obtained were collected by electrofishing during the fish sampling program in December.

After obtaining the total body weight to the nearest 0.1 g, a 6- to 14-3 sample of axial muscle (similar in weight to that taken from fish) was removed f rom the hind legs of each frog; placed in a preveighed 25- by 150-mm glass tabe; reveighed; and analyzed for 137 C s.134Cs, and 60C o using the same procedures described for fish.

2.4.3 Game Birds Several game bird species were collected in De cembe r from fields and sue 11 water bodies near Clay Creek downstream of the SMUD property line. Because the hunting season was closed for some species (e.g.,

ring-necked pheasant), a scientific collecting permit was obtained f rom the State of California, Department of Fish and Game. A shotgun was used for all collections. On both the November sad December sampling trips, waterfowl were not found la abundance on the stre am s or small ponds near the RSNPP. Generally, only a few ducks, sess!!y sellards, were observed at a given site. The low abundance and rather videspread distribution of waterfowl limited the collections to two coots.

Although recognized as a game bird by the State of California, which reguistes the hunting of this species, the coot is probably not as popular with hunters as is the mallard or teal (several species). Two ring-necked pheasants (a very popular game bird) and a single Wilson's snipe were also collected.

The total body weight of each bird was estimated to the nearest 13, and a 6- to 9-g sample of antal muscle was taken from the breast.

Analytical procedures were the same as those described for fish.

3. ENVIRONMENTAL SURVEY RESULTS 3.1 1TERNIRIAL BACKGROUND IEASUREMENTS Background external samma radiation levels 1 m above the ground were measured at a number of locations in the Sacramento Valley. Four locations, at distances of 6.4 to 16 km from the RANPP site and lying approximately north, south, east, and west of the site, were selected as having typical background levels for the general area. Gamma radiation exposure rates at these locations were very nearly uniform and averaged approximately 8 pR/h. Concentrations of radionuclides in soil at background locations averaged 0.41 pC1/g of 137C s, ef fectively zero pC1/3 of 134Cs, 0.73 pCi/g of 226A a, 0.77 pCi/g of 232Th, and 8.3 pC1/3 of 40K Background radionuclide concentrations in soil are given in Appendix A, Table A-1.

All direct meter readings reported in this document are gross readings; background radiation levels have not been subtracted because these readings were used for characterizing a location rather than quantifying the radionuclides present. Siellarly, background levels have not been subtracted from radionuclide concentrations measured in environment al samples. How ev er , doses from background locations were also calculated for comparison purposes.

3.2 EITERNAL GAMMA RADIATION LEVELS External gemma radiation levels were measured with samma scintillation counters (Nal). As discussed previously, comparison measurements were made with a pressurized ionisation chamber (PIC) at a number of locations in the fields and along the creeks. The relationship between these two sets of measurements was used to convert gamma scintillation counter measurements to approximate gamma dose rates in units of pt/h.

. Gamma radiation dose rates in irrigated fleids measured at 1 m from the ground surface ranged from background levels (8 pR/h) to about 14 pR/h. Gamma dose rates measured at the ground surface ranged from background levels to about 35 pR/h. Osame dose rates measured over slit <

deposits along Clay Creek were as high as 38 pt/h at 1 m and ranged up to 85 pR/h at the surface. Dose rate measurements taken along the banks 13

14 of Redselville Creek,15 m downstream from its confluence with Clay Creek, were 18 pt/h at 1m and about 60 pR/h at the esposed sitt surface. Surface radiation dose rates measured along Hadselville Creek approximately 3.2 km downstream from the entry of Clay Creek were as high as 37 pR/h.

3.3 SOIL SAMPLING As discussed previously, soil sample locations were chosen to provide sy st ema tic mabiased sampling (i.e., sampling locations were systematically chosen within an area showing nearly malform external samma radiation levels). Locations of samples that were analysed are shown in Figs. 3 through 8.

The primary radioactive contaminants fosed in soil sampl e s were 137Cs and 134C s with lesser amounts of 60Co and $3Co. Concentrations of 226 3 , 238g, 232Th. and 40K were generally at background levels. He nazimum concentrations of 137Cs and 134C s were 59 pC1/g and 23 pCi/s, respectively. Consistent with gamma radiation levels, the highest concentrations of radionuclides in soil occurred near the irrigation outlet pipes and decreased with distance from the pipes in the direction of water flow across the fields. The weighted average concentrations of 137Cs and 134C s are listed by fields in Table 2. Complete analyses results are gives in Appendis A, Table A-2.

3.4 VBGETATION SAMPLING Vegetation samples (pasture grass) were collected at locations immediately adj acent to soil sampling locations and in general were designated by numbers corresponding to those of soll samples.

Vegetation sample locations are given in Fiss. 3 through 7. As in soil, the radionuclides of primary laterest are 137Cs and 134C s.

Concentrations of 137Cs and 134C s as high as 6500 pC1/kg sad 2500 pC1/ks, respectively, were measured on a wet-weight basis in vegetation samples from irrigated fields. De concentrations of radionuclides in vegetation are distributed as in soil (i.e., higher near irrigation outlet pipes and decreasing with distance from the pipes la the direction of water flow across the fields). Average concentrations of 137 sC and 134Cs in vegetation samples are listed by

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21 Table 2. Average concentrations of radioactive cesium in soil, vegetation, and allt Soil and silta Vegetationb Average radionuclide Average radionuclide concentration (pCi/g, dry wt) concentration (pCi/kg. wet vt)

Field Number 137Cs 134Cs 137Cs 134Cs 1 2.28 0.84 2240 850 2 1.79 0.55 1220 890 3 1.52 0.59 85 55 4 1.37 0.44 1170 445 5 1.07 0.45 165 70 6 0.36 0.13 (27 (27 7 0.07 0.03 900 365 8 1.82 0.69 2170 840 9 2.97 0.49 2390 920 10 4.29 1.34 Not sampled 11 1.26 0.38 2680 2270 12c _ _

13c _ _

1. 31 3510 1460 14 75 15c - -

Snap 57 19 -

Pond 1 0.70 0.12 - -

Pond 2 6.0 2.1 - -

aAverage radionuclide concentrations in soil are weighted averages; individual concentration values are weighted according to the fraction of the total area represented by the sample bAverage radionuclide concentrations in vegetation are arithmetic averages, cFields 12, 13, and 15 showed only background levels of external gamma radia-tion and were not sampled.

dSamples collected under water (overflow) on field 14; nonflooded portions of the field were background.

22 fields in Table 2. Complete analyses results are given in Appendix A, Table A-3.

3.5 SILT SAMPLING Silt samples were collected from Clay, Hadselville, and Laguna creeks and from ponds and samps identified as having received water from Clay or Hadselville creeks. Sampling locations are shown in Figs. 3, 4, 7, a nd 8. As expected, the highest concentrations of radionuclides along the creeks are associated with silt deposits near obstructions or sharp bends in _the creeks and appear to be near background levels ir stretches of the stream bed where the stream flow is unimpeded and are subj ect to scouring during periods of high water flow.

The maximum concentrations of 137Cs and 134Cs (157' pCi/g a nd 65 pCi/g, respectively) were observed in Clay Creek near the RSNPP waste outfall and decreased downstream along Clay and Hadselville creeks, approaching background levels in Laguna Creek approxima t ely 19 km downstream from the plant site. Concentrations of 137Cs a nd 134Cs in water silt along Clay, Hadselville, and Laguna creeks are given in Table 3. Complete a na ly se s results are presented in Appendix A.

Table A-4.

3.6 WATER SAMPLING Water samples were collected from the RSNPP waste outfall, Clay, Hadselville, and Laguna creeks, a sump in field 1, ponds 1 and 2, and from a background station in Dry Creek (see Fiss. 3, 7, and 8 for locations). Two water samples (RSW001 from the RSNPP outf all and RSWOO5 from the mouth of Clay Creek) were subjected to radiochemical analyses.

The concentrations of all radionuclides analyzed were at or below the j minimum detection amounts (MDA) with the exception of tritium. The plant outfall sample contained 70,000 pCi/L of 3H, and the sample of water from the mouth of Clay Creek showed 9700 pCi of 3H per liter of water. Because of the low levels of radicnuclides found in these two samples and high flows observed in the creeks during the time of the survey, the rest of the water samples were not analyzed. Results of water sample analyses are given in Appendix A, Table A-5.

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23 Table 3. Concentrations of 137C s and 134Cs in silt samples from Clay, Hadselville, and Laguna Creeks.

Sample location Concentrations of radionuclide

- (pC1/g)

Sample Distance downstream No. from plant outfall (km) 137Cs 134Cs Clav Creek RSWS001 0.06 (200 ft) 157 1 1.7 65 1 4.9 RSWS012 0.55 86 1 1.3 35 1 2.7 RSTS006 0.71 115 1 1.6 45 1 3.2 Hadselville Creek RSWS005 3.2 97 1 1.2 42 1 2.4 RSWS004 4.0 58 1 0.73 24 1 1.9 RSWS034 (Background) 1.6 km 0.45 1 0.09 0.06 1 0.06 upstream from entry of Clay Creek Laanna Creek RSWS021 10 4.2 1 0.11 1.6 1 0.2 RSWS003 12 2.5 1 0.08 0.99 1 0.08 RSTS029 18 0.74 1 0.07 0.3210.05 RSWS002 19 0.26 1 0.06 0.15 1 0.03 aErrors associated with concentrations are 2 o (95% confidence l 1evel).

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24 3.7 BEEF SAMPLING Beef cattle are raised on land along Clay and Hadselville creeks. j These animals drink water from the creeks and graze on fields irrigated with water from the creeks. A cow was purchased. from the owner of the irrigated land; the animal was then slaughtered, and samples were shipped to ORNL for analyses. This cow, which was approxi ma t ely ten years old, had spent most cf its life on land bordering on Clay or

^

Hadselville creeks and had been removed from the irrigated pasture seven days prior to slaughter.

Four samples of beef, taken from dif ferent part s of the animal, and one liver s ample were analyzed by high-resolution gamma spectroscopy.

The result s of these analyses are given in Table 4.

3.8 HONEY SAMPLING A sample of honey collected from a hive on a ranch bordering Clay and Hadselville creeks was analyzed by gamma-ray spectrometry. The sample contained very little honey, mostly comb. The samma-ray spectrum contained only naturally occurring radionuclides with the exception of 137Cs. The 137Cs concentration was found to be 0 .0 06 1 0.004 pCi/ g .

The error given is the 2-o value for counting statistics alone.

3.9 FISH, FROGS, AND GAMF, BIRDS To estimate the dose to man from consumption of cont amina t ed fish and other vertebrates that are known to constitute at least a portion of the diet of same local residents, the concentration of radionuclides in the flesh (axial muscle) of both aquatic and terrestrial species was determined. The analyses were conducted on representative species of fish, frogs, and game birds from numerous locations in the vicinity of the RSNPP (Table 1). Results of these analyses are presented in Appendix A, Tables A-6 to A-9.

In the following discussion of these results, two maj or areas are empha s ized: (1) evaluation of the adequacy of the data for purposes of dose assessment and (2) interpretation of differences in the radionuclide concentrations in fish as a function of distance below the source and position in the food web (i.e., trophic level). The

25 Table 4. Concentration of radionuclides in beef samples from Rancho Seco Nuclear Power Plant environs Concentration of radionuclides (pCi/g fresh weight)s Sample Type 137 Cs 134Cs RSCM-1 Beck strap 0.01 0.005 RSCM-2 Shon1ders 0.009 ( 0.002 RSCM-3 Rib-eye 0.02 0.004 RSCM-4 Rond 0.009 ( 0.0' 04 RSCL-1 Liver 0.006 ( 0.0 03 "The counting errors associated with reported concentrations

. rang e from 1 20L t o 1 120%.

c

26 discussion is based on the results of the 137Cs analyses because it I contributes the majority of the dose to man from ingestion of contaminated biota (Sect. 4.1.1), because analytical accuracy is high and because most values are above the limit of detection.

3.9.1 Fish Estimates of the radionuclide concentrations in fish focused on three spe ci e s : green sunfish (or bluegill at some sites), largemouth bass, and black bullhead that inhabit the streams and small ponds near i

the RSNPP (Tables 5 and 6, respectively). Based on prelimina ry information from local anglers and our own sampling by electroshocking, these species comprised the majority of the sport fishery in these sma ll ponds and streams. Black crappie, which were collected at only one site (upper Laguna Creek at Laguna Road), were also included because of their importance as a game fish in other regions of the country.

A valid assessment of the radiological dose to man from ingestion of contaminated fish must take into account the size, as well as the species, of fish that local anglers might keep for consumption. Size is especially important because the concentration of some radionuclides may be higher in the larger (older) individua l s in the population. For example, Kolehmainen a nd Nelson (1969) found a direct linear relaticnship between total concentration of 137C s and weight of bluegill over a range of weights from 1 to 70 g (Y = 9.26 + 0.391, r2 = 0.998);

concentrations of 137 C s (Y) in bluegill (I) increased by a factor of 4 over this range. In addition, they found no correlation between the concentration of 137Cs and weight in fish greater than 70 g, and they attributed this to the fact that the 137Cs concentration in these larger fish was in a steady state. A regression of the 137Cs concentration in axial muscle and body weight for seven bluegill (weights ranged from 70.7 to 192.7 g) collected from a sump near the SNUD property line in Novemb e r 1984, (1 A-7) indicated that fish exceeding 70 g did not have increased concentrations of 137Cs. The slope of the regression line (Y

= 9.93 - 0.031,* r2 = 0.41) was not significantly different from zero

[t-test, P (probabilitf} >0.05 (Snedecor and Cochran 1967)] .

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Table 5. Ilean ooneentration (pCi/s. wet ut.) of radionnelldes la salat masels of fish collected from streams downstrees of the Rasche Seco Nuclear Power Plant. December 1984.

(Less then values ignored is compattom of mees; a = 3 for each speeles/ site combination)

Species Green saatish Largemouth base Black crapple Black ballhead Se as I37 ## 33# #I Ce *Cs

• Co Ce 'Ce

• Co Ce 'Cs Co Cs 33*Ce

• Co Clay Creek 10.03 4.75 0.38 8.96 4.07 0.42 NC* 7.16 3.60 0.36 (1.73)b (0.77) (0.25) (1.51) (0.78) (0.11) (0.72) (1.01) (0.38)

Bedeelville 6.58 3.13 0.29 NA* NC 9.21 4.41 0.44 Creek (3.46) (1.28) (0.20) (1.57) (0.65) (0.09)

Lassan Creek 0.67 0.28 0.28 NA 1.58 0.78 0.15 0.40 0.39 0.46 et Lagene Ed (0.27) (0.33) (0.22) (0.37) (0.12) (0.17) ( 0.3 9 ) (0.12) (0.19)

1. d Lessee Creek 0.13 0.07 0.40 NC NC 0.09' (0.05 0.23 at Noteamto Ed (0.12) (0.02) (0.06) ,

w Dry Creek 0.05 0.12 0.44 NC MC NC (control) (0.01) (0.13) (0.34)

• Nome collected.

Numbers is parentheses !adiente st andard deviet toa.

'None emetysed; all individmete collected were emelt.

a = 1.

Table 6. Noes concentration (pCl/s. wet vt.) of radionsolides la asial mesels of fish collected from emell ponds meer the Beacho Seco Nuclear Power Plant, November-December 1984.

(Less thaa valses ignored la compattom of mesa; a = 3 for each species / site combination)

Specie s Green suefish Blaegill Largemosth boss Black bullhead Sampling 3 3 3I 'U I37 'Cs

• Co *Cs

• Co 3*Cs e I3*Cs

• Co Cs Cs Cs Co D

Samp NC' 6.35 3.03 0.12 15.20 7.03 0.50 6.29 3.04 0.18 (2.13)* (1.22) (0.19) (1.34) (0.82) (0.09) (2.67) (1.22) (0.17)

Pond 1 NC 0.35 0.05 0.60 0.17 0.06 0.21 NC (0.27) (0.01) (0.07) (0.06) (0.04) (0.19)

Pond 2 0.36 0.17 0.31 NC 3.16 1.33 0.24 0.91 0.41 0.49 (0.40) (0.13) (0.26) (1.53) (0.86) (0.09) (0.29) (0.61) (0.13) w e

"Noas collected.

m = 8.

'Nambers la parentheses indicate standard deviation.

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r __

29 .

k The existence of a' concentration-vs-size relationship in smaller bluegill (<70 g) emphasizes the importance of limiting the analyses of radionuclide concentrations in fish flesh to the larger individuals in the population. We have assumed that similar relationships between radionuclide concentration a nd size exist for the other species, although the weight above which concentrations no longer increase with increasing size is not known. Consequently, a minimum size criterion based upon the shape of the curves could not be used to evaluate the adequacy of the fish data used in the dose assessment calculations (Sect. 4.1.1.1) (i.e., to identify those samples with low radionuclide concentrations because the fish were small and not because levels in the environment are low).

As an alternative approach, minimum size criteria were selected for r

each species based on angler preference (Table 7) . Overall, 55% of the fish collected met a minimum size criterion based on quality length, or the size of fish most anglers like to catch [ Anderson (1980), as cited in Gabelhouse (1984)]; and 65% of the fish collected were within 1 cm of

the criterion. Criteria based on minimum quality-length may approximate the criteria derived f rom the concentration-vs-size relationship. For

example, the minimum quality length for bluegill is 15 cm, total length (or 12 cm standard length) . Using the length-weight regression computed for bluegill collected from the samp and pond 2 (Table A-7, footnote c),

the estimated weight of a 15-cm bluegill is 68.6 g, very similar to the 70 g criterion based on data in Kolehmainen and Nelson (1969) . Such

[

close agreement between the two criteria should be viewed with caution i because (1) growth rates of bluegill in the two environment s may be I different and (2) no data are available for other species.

Similarly, the minimum quality length criteria used in our analysis should be considered as guidelines. Angler preference will vary between individuals and between water bodies because of differences in the availability of fish of quality length to the angler. Because small s t r e am s , such as Clay Creek, may have very few largemouth bass that exceed 30 cm (12 in.), 1ccal fishermen may keep bass that are less than 30 ca. Although only 50E of the Isrgemouth bass collected in December 1984 exceeded 30 cm, all but one (92%) exceeded 25 ca; therefore, l residents might be expected to consume fish of the smaller size. It is

JO Table 7. Percentage of the fish analyzed for radionuclides that exceeded the minimum quality length proposed by Gabelhouse (1984)

Species Total ampling (All species site Green Largemouth Black Black combined)

Bluegill sunfish bass crappie bullhead Minimumqualitg 15(6) 15(6) 30(12) 20(8) 23(9) 10rgth, ca"'

City Creek 100 0 33 44 H:dasiville Creek 67c 100 83 Lageca Creek at 67 33c 33 44 Laguna Rd.

Laguna Creek near 0 0 0 McKanzie Rd.

Dry Creek (control) 67c 67 Snap 88c 67c 67 79 Pand 1 100 100 100 Pard 2 0 33 OC 11 Tatsi (all sites 50 91 50 33 44 55 sombined)

U Quality length is defined as the size of a fish most anglers like t catch (And3rson 1980 as cited in Gabelhouse 1984).

Length in inches in parentheses.

Excludes one fish that was within 1 cm of the minimum quality length -criterion.

t

32 these fish, all the others in Table A-6 exceeded the minimum quality-length criterion of 12.ca standard length and weighed more than 60 g.

Moreover, mean weights at each site exceeded 68 g (range: 69.4 3 in Dry Creek to 85.7 g'-in Clay Creek); these mean weights were similar to the 70 g value reported by Kolehmainen and Nelson (1969) as the weight above which concentration and size vere not correlated in the bluegill, a species closely related to the green sunfish. For these reasons, any bias in comparing concentrations of radionuclides in fish with different weight distributions is assumed to be minimal, and adjustment of the concentrations to a standard fish based on regression analyses would not alter the conclusions that follow.

Radionuclide concentrations in green sunfish declined with increasing distance downstr e am of the source at the RSNPP (Table 5).

Although the three sampling stations bel ow the plant were about equidistant apart (4-5 km), the greatest reduction (by a factor of approximately 10) occurred between the Hadselville Creek- and upper Laguna Creek sites. Cesium concentrations in green sunfish from Hadselville Creek were only 35% lower than the concentrations in the same species from a site on Clay Creek approximately 0.5 km below the outfall of the plant. Silt concentrations were approximately 25% lower in Hadselville Creek (sites RSTS004 and RSWS005) compared with concentrations in Clay Creek (sites RSTS006 and RSTS012) (Table A-4).

Concentrations in black bullhead were actually higher in Hadselville Creek, probably because the individuals were, with one exception, larger at this site. However, the distribution of weights varied between the two sites, thus direct comparisons are difficult. An unambiguous conclusion based on the data from both species is that fish fron l Hadselvile Creek have cesium levels that are not much l ower than the levels in Clay Creek, about 4 km upstream near the SMUD property line.

Although concentrations of 137 C s in fish decline shstply below the confluence of Hadselville and Laguna creeks, they are still at least an order of magnitude above background approximately 9 km below the plant (upper Laguna Creek vs Dry Creek sites).

Finally, comparisons between species at a given site indicated that the concentration of 137Cs in piscivorcus species (fish-eaters, such as largemouth bass and black crappie) exceeded that of nonpiscivorous

31 not known if the radionuclide concentrations in these bass are near the maximum.

The minimum quality-length criteria were needed to identify potential bias (underestimates of radionuclide concentrationt.) in the data base resulting from the inclusion of small fish. Our analyses indicated that, except for the lower Laguna Creek site (near McKenzie Road), an adequate sample (i.e., fish large enough to be kept by anglers) of at least one species was obtained from the other seven sites. Of the four fish analyzed from lower Laguna Creek, only one approached a size that might be included in the catch of local anglers.

Radionuclide concentrations in all four fish were very low- and similar to the concentrations found in fish from Dry Creek, the control or background site located approximately 17 km east of the power plant.

However, the data from the Laguna Creek site are biased low because most of the fish collected at the site were small.

Similar comparisons of the radionuclide concentration in fish from other sampling sites are subj ec t to the s ame bias because of the differences in fish weight's between sites. To correct for such bias, empirical. relationships (linear regressions) between concentration and weight must be derived for each species-site combination. For a given species, radionuclide concentration values at each site can be normalized by adjusting them to the concentration in a standard fish (e.g., a 70 3 bluegill), using these site-specific regression equations.

Such an approach was used by Elwood (1984) and Van Winkle et al. (1984) to make between-site comparisons in the concentrations of mercury, another contaminant in which concentrations in muscle tissue are correlated with fish weight. Because only the three largest individuals of a species were analyzed at each site, a regression analysis of the Rancho Seco data is not appropriate.

Without the support of statistical analyses, comparisons between sampling sites will be less rigorous and, by necessity, conservative (i.e., tending to overpredict the radionuclide concentration or dose).

The only species that can be used for such comparisons is the green sunfish, which was similar in size at most of the stream sampling sites, except lower Laguna Creek, as noted previously, and upper Laguna Creek where one of the three individuals was small (Table A-6). Excluding

. 33 species in three of five possible comparisons; in Clay Creek and pond 1, concentrations of 137C s were higher in sanfish than in largemouth bass.

Numerous studies have reported higher bioaccumulation factors for 137Cs in piscivorous compared to nonpiscivorous species [see review by Vanderploeg et al. (1975)], although the ratio between the two groups varied between study sites. The bioaccumulation factor for 137 Cs recommended by Vanderploeg et al. (1975) for piscivorous fishes was approximately three times higher than that for nonpiscivorous species.

Several factors may account for the results obtained in Clay Creek and pond 1. First, individuals of the prey species (sunfish) collected at both sites were very large and may not represent the preferred food of the predator (largemouth bass). Bass cf the size collected from the two sites may feed on smaller individuals (with correspondingly lower 137Cs concentrations) or on species different from those included in this analysis. Second,137 C s may not be equally available to the two species because clay particles can alter the efficiency of 137 Cs assimilation [Kolehmainen and Nelson (1969)]. Eyman and Kitchings (1975) found that 137C s accumulation in bluegill and channel catfish can be greatly influenced by sediment composition, particularly the cisy and organoclay c ompl e xe s , which affects the availability of cesium for l

assimilation. Differences in sediment composition between the eight sampling sites are not known. Although detailed information on food habits (e.g., prey species and size as a function of predator size) and

! sediment composition were not collected, the available evidence, both

from this study and others, suggests that the highest concentrations of 137Cs and 134Cs, which will not have an appreciably different bicaccumulation factor than that of 137Cs (Vanderploeg et al. 1975),

should occur in piscivorous species, such as the largemouth bass.

3.9.2 Frons The three individuals that were analyzed for radionuclides were collected from the two sites (pond 1 and l owe r Laguna Creek near l McKenzie Road) with the lowest levels of contamination (Table A-4).

Conse que ntly, radionuclide concentrations in these frogs may be lower than if they were collected in more highly conterinated sites (Table A-8). The sus 11 sample size [one frog at each site, after l

34 excluding a very small (37 g), unrepr e se nta tive individual from lower Laguna Creek] restricts the use of these data for dose assessment.

Because the frogs were collected from sites with the l owe s t levels of cont amina ti on, these data cannot be used to estimate concentrations in frogs at other sites with much higher levels of contamination.

To resolve this problem, radionuclide concentrations in piscivorous fishes could be used to provide an estimate of the maximum concentrations that might be expected in frogs from these sites. The rationale for this approach is the similarity between the recommended bioaccumulation factor (the ratio of the concentration of a radionuclide in fish to its concentration in the water) for cesium in amphibians and that for piscivorous fishes (~104 ) [Vanderploeg et al. (1975),

Table 1)]. Support for the conservatism of this approach is based on data from pond 2 (Table A-7) . The concentration of 137C s in each of the six fish exceeded that of the large (293 g) bullfrog. Although the sample size is admittedly small, all the samples were taken from very large individua l s, so the confounding effect of body weight on concentration is minimized.

3.9.3 Game Birds Five game birds (three species) were collected at various sites near Clay Creek between 0.5 and 3.0 km downstream of th e RSNPP (Table A-9). Concentrations in all samples were relatively lew and substantially lower than the concentrations in fish from Clay Creek.

, Although local sportsmen probably prefer to hunt (and est) other species I

i of waterfowl (e.g., mallard, teals) than the American coot, these species were uncommon inhabitants of Clay Creek and the small ponds nearby during the sampling periods. Even though the coot has different food habits than many other waterfowl, preferring primarily aquatic j vegetation to grasses or grains [ Bent (1926)], the data on radionuclide concentrations in this species may approximate or exceed the concentrations found in other waterfowl. Bioaccumulation f actors for 137Cs in muscle tissue, for example, were estimated by Pendleton and Hanson (1958) to be if 00 and 2000, for the American coot and mellard, respectively. Moreover, the American coot is a year-round resident in the southern portion of its range [ Bent (1926)]. If this includes

35 Sacramento County, their exposure to contamination von 1d be greater than that of other species that are migrants in this region and breed in more northern latitudes. D e winter and . breeding ranges of the American coot, on the other hand, include California [ Bent (1926) ] .

1 1

i c

i i

i I

l l

4. RADIATION DOSE ASSESSMENT Radiation doses associated with the 11gald radionuclide. releases from the RSNPP were estimated for a number of potential pathways of external and internal exposure. Me a s ureme nt s of radionuclide concentrations in environmental media and edible food sources in the vicinity of Rancho Seco indicated that only 60Co, 134Cs and 137C s would contribute significantly to radiation doses which might be received by an individual. In addition to estimates of dose made directly from measured samples, several model calculations were made to indicate the magnitude of potential pathways of exposure associated with local contaminated land.

4.1 PATINAYS OF IhTERNAL EIPOSURE

! Individuals living around Rancho Seco say be laterna117 exposed to radiation doses via ingestion of contaminated foods and inhalation of radionuclides from contaminated land areas. Aquatic species such as fish and frogs living in contaminated waters and terrestial species such as coots, pheasants, and beef cattle on lands contaminated by irrigstion or overflow of Clay Creek all represent potential sources of radiation dose to individuals. In addition, the consumption of vegetables grown on contaminated land and the consumpton of drinking water are considered as potential pathways of internal exposure. The resuspension in air of contaminated soil particles or the release of radioactivity from burning of vegetation represent potential dose pathways via inhalation.

f All estimates of dose from pathways of internal exposure were made using dose conversion factors and models contained in the latest version of NRC Regulatory Guide 1.109 [USNRC (1977)]. Internal dose s are calculated for ingestion or inhalation pathways. The dose from the ingestion pathway is given by [USNRC (1977)].

I (DFI ),

D"8=(Cf) (Uf) 3 where DIg *3 = annual dose commitment to an indivivual one to the ingestion of radionuclide 1 (area) 37

38 concentration of radionuclide i in ingested food Cf =

(pC1/kg) annual intake (asage) of food containing radionuclide Uf =

1 (kg) and DFI g = ingestion dose conversion factor.for radionuclide 1 (aren/pC1).

Similarily, for the inhalation pathway [USNRC (1977)],

Dfah , - (C") (R,) (DFAg ),

where Dg inh = annual dose commitment to an individual due to the inhalation of radionuclide 1 (ares)

C" = concentration of radionuclide i in air (pC1/m 3);

R, = annual air intake for individuals (m 3) and DFA = inhalation dose conversion. f actor for radionuclide 1 (ares /pci).

In this study it was assumed that R, = 8000 m3 [Rapp (1984)].

1 4.1.1 Innestion 4.1.1.1 Ehh Consumption of local fish represents the primary potential pathway of dose to individuals from RSNPP lignid ef fluents. Table 8 gives total-body and critical organ (liver) doses resulting from the lagestion of 1 kg of fish for eight locations. These values are based on average radionuclide concentrations in fish caught at the eight locations. Fish from Clay Creek, the sump near the SMUD boundary, and Hadselville Creek at Clay Station Road are the critical locations. Radionuclide concentrations in fish at these locations result in doses of 1.1, 1.3, and 1.0 mrea total-body dose /kg ingested, respectively. Dose to liver, the critical organ, is about 1.4 times greater. Thus, consnaption of 14, 16, and 18 kg, respectively, of fish per year from these locations could give an estimated organ dose to an individual which would be at the 25 aren/ year limit given in 40 CFR 190 [USEPA (1977)].

39 Table 8. Radiation doses from ingestion of fish caught in the vicinity of Rancho Seco Dose (ares /kg ingested)

Location Number of Total body Liver samples Clay Creek at 9 1.1 1.6 SNUD boundary Samp 6 1.3 1.8 Pond 1 adj acent 6 0.03 0.04 to field 2 Pond 2 near 9 0.17 0.24 Silva's feedlot Hadselville Creek at 6 1.0 1.4 Clay Station Road Laguna Creek at 9 0.12 0.17 Laguna Road Laguna Creek at 4 0.007 0.01 McKenzie Road Dry Creek at Ete. 104 3 0.02 0.03 (control) i

40 Consumption of fish from other ponds in the area or from loca t ions

-downstream from the Hadselville Creek sampling location appear to pose no problem because it is completely unlikely that as ladividual von 1d have a yearly consumption of fish great enough (150 to 3500 kg) to exceed the 25-aren limit.

Radionuclides contributing to the dose from consnaption of fish are 137 C (55.3%), 134Cs (44.5%) and 60Co (0.2%).

4.1.1.2 Froms and name birds Based on measured concentrations of radionuclides in frogs and game birds, consnaption of these foods would result in very small total-body radiation doses (Table 9). However, frogs were not sampled at the most contaminated locations. If it is assumed that frogs would contain about the same concentrations of radioactivity as fish sampled in these locations (see Sect. 3.9.2) a dose of about 1 ares /kg ingested would result from consumption of frog flesh in the most contaminated areas.

4.1.1.3 Venetables Although vegetables are not currently grown in any of the contaminated, irrigated fields around RSNPP, an estimate was made of potential dose from consumption of leafy vegetables. Using models from Regulatory Guide 1.109 [USNRC (1977)] and average radionuclide concentrations in soll sampled from field 1 (the most contaminated field), it was assumed that an individual eats leafy vegetables grown in this field. The resniting ananal dose would be 3 x 10-5 ares /kg ingested to the total body, 5 x 10-5 ares /kg ingested to the liver.

This estimate is conservative because most of the soll samples taken in field I were taken in small areas where relatively high external l exposure readings were given when the field was surveyed in a walk-over.

While this pathway of exposure is not currently available, the dose estimate se rve s to indicate that ladividual exposares from consamption of vegetables grown on this area would lead to less dose than would consumption of fish from the most contaminated aquatic sampling locations.

41 Table 9. Radiation doses from ingestion of frogs and game birds caught in the vicinity of Rancho Seco Dose (=1111res/kg ingested)

Number of samples Total body Liver Frogs 3 0.01*(1.1) 0.02*(1.6)D American coot 2 0.02 0.02 Pheasant 2 0.02 0.03

" Dose based on measured activity.

Dose based on assnaption that frog flesh contains the same activity as fish flesh.

I i

1

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42 l

i 4.1.1.4 Rigi i

Two estimates are given of the total-body dose to an individual )

eating beef from cows allowed to graze on fleids 1 and 2 (Table 10).

Analysis of beef samples from a cow slaughtered December 27, 1984, indicated very low levels of 137C s and 134Cs (1.08 x 10-2 and 3.6 x 10-3 pCi/g, respectively) . This cow was assumed to have grared on fields 1 and 2 for several months. The resulting dose of 1.2 x 10-3 arem/ year (total body)/kg of beef ingested is indeed small. Estimated concentrations (USNRC, (1977)] for 137Cs, 134 Cs, and 60C o in beef based on average values of grass samples led to an estimated total-body dose of 4.6 x 10-2 ares / year per kg ingested. This estimate is conservative, however, in that more grass samples vers taken in small areas with the heaviest contamination in fields 1 and 2. Also, the model cow is receiving only contaminated pasture in its diet.

It is not likely that consumption of beef from cows allowed to graze in contaminated fields mround Rancho Seco would lead to doses greater than 1 ares / year to an ladividual.

4.1.1.5 Mill Although milk cows are not raised on the contaminated fleids around Rancho Seco, an estimate of dose via ingestion of milk was made using Regulatory Guide 1.109 models and average concentrations of radionuclide in grass sampled in fields 1 and 2.

Consumption of milk would lead to a total-body dose of 0.14 ares /1 ingested (99.9% due to cesium radionuclides). Because of the relatively high cesium transfer factor from grass to milk, allk consumption leads to higher doses than does consumption of beef. Although these estimates are conservative due to biased sampling of grass, the use of fields 1 and 2 for heavy grazing by milk cows could lead to doses close to the 25 ares / year limit if it is assumed that all of the allk ingested by the maximally exposed individual comes from cows grazing on these contaminated fields.

43 Table 10. Radiation doses from ingestion of beef Dose (millirea/ year /per kg lagested)

Source Total-body Liver Sampled cow 1.2 x 10-3 1.7 x 10-3 Nodel cow" 4.6 x 10-2 6.3 x 10-2

• Concentration of radionuclides in beef calculated from grass samples in fleids 1 and 2.

1

44 4.1.1.6 Yater Water from local s t r e'an s carrying RSNPP liquid wastes is not consumed directly by man. However, an estimate of dose was made which indicates that no serious problem would be anticipated for this potential pa tty sy of exposure. An apper Itait of potential dose was estimated by assaming that an individual drinks water at the Rancho Seco outfall. The resulting total-body dose was 7.8 x 10-3 area /L ingested with 94.4% from 3H, 5.4% from cesium, and 0.2% from other radionuclides.

4.1.1.7 Honey Honey collected from a hive on a ranch tordering Clay and Hadselville Creeks contained small concentrations of 137C s (0.006 pC1/3) 134 and naturally occurring radionuclides. No Cs was found in these samples. Ingestion of this honey would result in a total-body dose of 4.3 x 10-4 area /kg ingested for the 137C s. This level of 137Cs could result from weapons fallout [ United Nations Scientific Committee on the Ef fects of. Atomic Radiation (UNSCEAR) (1977)]; thus, it would seem that ingestion of honey poses no significant radiation dose pathway in the RSNPP area.

4.1.2 Inhalation 4.1.2.1 Transuranic Radionuclides A soil sample taken near the RSNPP outf all contained small amounts of transuranic radionuclides (238Pu, 239pa, 241Am, and 244Cm). The total activity was 1.1 x 10-2 pC1/3 It is estimated that 1 m2 of soll would contain 179.2 pC1. Resuspension of these radionuclides into air by an amount of 10-9/m [Eckerman and Young (1980)] would lead to a lung dose of 1.2 x 10-6 mrom for an individual breathing 8000 m 3 of air for one year. Any plausible ingestion pathways would lead to even smaller doses. Therefore, transuranic radionuclides seem to pose no significant radiation dose problems. Indeed, the levels of transuranic radionuclides found in the RSNPP environs are consistent with levels reported for weapons fallout [USEPA (1976)].

45 4

4.1.2.2 Other Radionuclides The resaspension into air of montransaranic radionuclides la soil l l and subsequent inhalation by an individual represents one pathway of internal exposare around Rancho Seco. A dose estimate for this pa thw ay was made by assamlag average soil contamination levels la field 1 and a resaspension value of 10-9/m for aged deposits. Total-body dose to sa individual breathing these resaspended radionuclides was estimated to be 3.0 x 10-4 mres/ year. Because no individual would be exposed -to this pathway for a in11 year, a dose of about 3.4 x 10-6 ares for 100 h of exposure is more realistic. During cultivation, more deposited 1 radioactivity is resaspended (10-5/s) so that sa individual spending 100 h/ year cultivating field 1 von 1d receive an estimated total-body i dose of 3.4 x 10-2 area. These inhalation pathways would contribute little to maximum individual doses for pe r sons stilizing contaminated fleids around Rancho Seco.  :

1 Another potential inhalation pathway is associated with burning contaminated vegetation. Because rice is raised in the Rancho Seco ares )

and the stabble on-rice fields is barned, dose from this pa thw ay was

estimated. It was conservatively assumed that field 1, with the highest i levels of contamination, was used for cultivation of rice. It was ,

further assumed that stubble mass (2.0 kg/m2) contained the same level i

of contamination as grass sampled from field 1. Thas a total inventory of 156 pCi of 137 C s, 59 pCi of 134C s, and 3 pCi of 60Co contained in the 3.5-ha fi61d (8.61 acres) was assumed to be released in a fire of 30 min duration. Usics an atmospheric dilation factor of 3.6 x 10-3 s/m3 , en individual 100 m from the fire who inhaled contaminated air for the duratio'n of the fire would receive a total-body dose of 1.3 x 10-2 ,,,,,

Thus, the inhalation pathway associated with barmlag of contaminated vegetation aromad Rancho Seco would seem to pose no significant dose problem.

4.2 PA11tWAYS OF EXTERNAL EIPOSURE Two pathways of external exposure are available for individuals around Rancho Seco. These are exposure from contaminated ground and exposare from swimming la contanlaated water. Again, using average vaines of soil contaalmation in samples from field 1, an amasal total- l

, body dose of 73 aren/ year was estimated. Since no individual is exposed .

l l

44 for one year, a more realistic dose of 0.83 area is estimated for 100 h of exposure per year.

Swimming for 100 h/ year in water contaminated to the same degree as water collected at the plant outfall would lead to a total-body dose of 1.6 x 10-3 mrem.

4.3 ALTERNATE DOSE (X)NVERSION FACTORS The internal dose conversion factors contained in USNRC (1977) were used in the calculations reported above. However, more recent vaines based on models proposed by the International Commission on Radiological Protection (1977) are available [ Dunning et al. (1981)]. For the principal radionuclides considered in this study, these never vaines are lower than the dose conversion factors given in USNRC (1977) . For example, use of the values from Danning et al. (1981) wonid lowe r the total-body doses due to ingestion of 134Cs by 44% and those due to ingestion of 137C s by 31%. For inhalation, redactions in total-body dose would be 53% for 134Cs and 42% for 137Cs. Doses to liver, the critical organ, would be reduced by less--28 to 38%. It may be more appropriate to use the dose conversion factors given by Dunning et al. (1981) than those contained in Regulatory Guide 1.109

[USNRC (1977)] if the risk to persons living near the RSNPP is to be calenisted.

5. INVDTIVRY OF RADIONUCLIDES IN IRRIGATED FIELDS Soil samples were collected and analyzed from 45 locations in the irrigated fields and silt was collected from three locations each in the samp and ponds 1 and 2. Based on the concentrations of 137Cs and 134Cs found in the soil and silt samples, an estimate of the amounts of these radionuclides remaining in the fields and in the semp and ponds was made.

Each field was divided into areas based on the surface gamma radiation levels observed in each area. Soil sample result s from each area were averaged and the' averages were weighted according to the fraction of the area of the field represented by the respective areas.

Figure 9 shows a typical division of a field into areas for averaging and weighting results. Th e weighted average concentration for eech field was combined with the average sample weight, the area from which the samples were collected, and the area of each field to arrive at an estimate of the quantity of each raditsuclide contained in each field.

The relationship used in these determinations is as follows:

g, AK(C, - CB) ,

109a where

! Q = quantity;of radionuclides in field in sci, A = area of field in ft2, K = average weight of sample in g, 1

Cs = weighted average concentration of radionuclida in pCf/g, i

CB = background concentration of radionuclide in pCi/g, and a = 0.1964 ft2, area of sample plus (6-in. slaaeter).

If substantial areas of a fleid showed the concentration of radioactive contaminants to be at background levels, a weighted average was not used in determining the quantity of cesium in that field, but the quantities of radionuclides were determined for' each individual area.

47

i s,s 44 '

\ .N, Nx s N N

\ ~N.,

x a  :  :- a a a  :  : :

a  ; i a rIRRIGATION OUTLETS -*o

% o o o o o*-

, _ _ SECTION_ _ _ A_ _ _ _ - - - - - - -

B a IRRIGATION FLOW SECTION B l

8 E

I J

B SECTION C a

l Il SECTION D a

I lL 1,

a a 1 1 I E I E I  : E 5 1 1 TYPICAL IRRIGATED FIELD Fig. 9. Typical irrigated field showing division into sections for use in arriving at weighted average radionuclide concentrations.

i 49 l

Table 11 lists the estimated quantities of 137Cs a nd 134Cs contained in each field, the snap, and ponds 1 and 2. Analyses of depth l samples taken from the fields indicates that approximately 85% of the radioactivity is contained in the top two inches of soil. This correction has not been applied ~to the values in Table 11.

Reported releases from RSNPP during the period 1981-1984 were 280.9 aci of 134Ci and 520.6 aci of 137Cs (Table C-1). The quantity of 134Cs, when corrected for decay, becomes 174.1 aci of 134Cs remaining at the time the survey was carried out. Using the corrected decay value for 134Cs discharged (174.1 aci) and correcting the total quantities of radionuclides from Table- 11 for the 15% of the radioactivity not sampled, the estimated inventory accounts for about 21% of the 137Cs and about 25% of the 134Cs released from the RSNPP during the period 1981-1984.

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SO Table 11. Ceslam inventory in fields, samp, and ponds 1 and 2 Quanity of radionuclide(aci)

Location 137 134 g, Field 1 7.40 3.17 Field 2 2.99 1.07 Field 3 4.18 1.66 Field 4 1.89 0.76 Field 5 1.11 0.66 Field 6 0.72 0.45 Field 7 7.21 2.97 Field 8 6.89 2.81 Field 9 12.31 4.97 Field 10 14.62 4.87 Field 11 6.10 1.69 Field 12 Not sampled Field 13 Not sampled Field 14 23.50 9.52 Samp 4.81 1.61 Pond 1 0.09 0.02 Pond 2 0.87 0.32 1

Total 94.68 36.55

6.

SUMMARY

OF RESULTS The release of radioactive materials in the liquid waste effluents from the RSNPP has resulted in elevated concentrations of some j radionuclides in the immediate environment of the plant. The l radioactive contamination in the environment occurs primarily along streams receiving effluents from the plant and in fields irrigated with water from these streams. The highest levels of radionuclides (approximately 375 times background concentration of radionuclides measured) occur immediately below the plant liquid waste outfall and decrease with distance from the plant downstream along Clay and Hadselville Creeks and approach background levels approximately 19 km from the plant in Laguna Creek. The primary contaminants are 137Cs and 134Cs with lesser amounts of 60Co and 58Co.

Radionuclide concentrations in fish also declined with increasing distance downstream of the RSNPP. Concentrations in green sunfish from Clay Creek at the plant bounda ry were 200 times the background concentration of the radionuclides measured and decreased by 39% in Hadselville Creek,.approximately 4 km down s t r e am. Although the s ame distance separated the Hadselville Creek and upper Laguna Creek sites, concentrations in fish decreased by almosr an order of magnitude. The highest cesium concentrations occurred in largemouth bass collected from a sump at the boundary of the RSNPP'(mean sr. lues of 15.20 and 7.03 pCi/g wet weight for 137Cs and.134Cs, respectively). At three of five sites, cesium concentrations were higher in piscivorous (e.g., largemouth bass) than in nonpiscivorous species.

Elevated external gamma dose rates are associated with the radioactive cont amina ti on in the irrigated fields and along streams receiving ef fluents from the plant. Gamma dose rates up to 38 pR/h at 1a from the ground were measured along Clay Creek, and the maximum gamma dose rate measured in irrigated fields at 1 m was about 14 pR/h.

Table 12 gives doses estimated for an individual who might be exposed to the currently available pathways. This estimate also serves to indicate the relative importance of the dose from ingestion of fish.

Specific pathways of exposure and usage factors were not precisely known for this analysis of current and potential use of contaminated water and 51

$2 Table 12. Potential radiation doses to an individual from Rancho Seco liquid effluents

• Dose (alllires per unit esposure)

Source Tostal body Live r Internal Consumption of fish (per kg) 1.1 1.6 Consumption of frogs (per kg)* 1.1 1.6 Consumption of gamebirds (per kg) 0.02 0.03 Consumption of beef-(per kg)d 0.001 0.002 Inhalation of resuspended material

• 0.03 0.05 Inhalation of vegetation fire 0.01 0.02 External Contaminated ground 8 -0.83 0.83 Swinning I 0.002 0.002 "These doses cannot be added together without considering actual consumption or exposure data.

b Average dose for three most contaminated areas.

• Assumes frog flesh is as contaminated as fish flesh.

Dose based on measured sample.

• 100 h/ year cultivation.

I Duration of fire is 30 min.

8 100 h/ year.

i

53 soil around Rancho Seco. However, it seems reasonable to assume that maless same individual is eating 14 to 18 kg of fish per year caught in the sump, Clay Creek, or Hadselville Creek at Clay Station Road, a 25-ares / year dose limit [USEPA (1977)] is not reached by any individual around Rancho Seco.

No attempt has been made in this study to estimate annual doses associated with each year of release. Rather, this study gives estimates of dose associated with current e nvi ronme nt al levels of cont amina tion and potential pathways of exposure. Assuming no further liquid radionuclide releases from the RSNPP, future maximum individual doses should be no greater than those estimated here because of radiological decay and additional dispersion of contamination in .the envi ro nne nt . -

l _ , _ - - - - - -

7. REFERENCES Anderson, R. O. 1980. " Proportional stock density (PSD) and relative weight (Wr): Interpretive indices for fish populations and communities." In: Proc.. Practical Fisheries Mannaement: More with Less in the 1980's. S. Gloss and B. Shupp (eds.)., American Fisheries Society--New York Chapter, Ithaca, New York, pp. 27-33.

Be nt , A. C. 1926. Life Histories of North American Marsh Birds.

Smithsonian Institution U.S. National huseum Balletin 135. U.S.

Government Printing Office and Dover Publications, Inc. (1963), New York, p. 392.

Danning, D. E. , Jr. , G. G. Killough, S. R. Bernard, J. C. Pleasant, and P. J. Walsh. 1981. Esta==tes of Internal Dose Ennivalent to 22 l Tarmet Ormans for Radionnelides Occurrina in Routine Emleases from Nuclear Fuel-Cycle Facilities. Vol. III. NUREG/CR-0150 (ORNL/NUREG/TM-190/V3), Oak Ridge National Laboratory, Oak Ridge,

. Tennessee.

I Eckerman, K. F. and M. W. Young. 1980. A Methodoloav for Calculatina Re sidual Radioact ivity Levels Fo11ovina Decommissionina. NUREG-I 0707, U.S. Nuclear Regulatory Commission, Washington, D.C.

i Eddy, S. 1969. The Freshwater Fishes. W. C. Bt en C mpany, o Dabuque, i Iowa, p. 286.

Elwood, J. W. 1984. Mercury Contamination in Ponlar Creek and The Clinch River. ORNL/TM-8893, Oak Ridge National Laboratory, Oak Ridge, Tennessee, p. 60.

Eyman, L. D. and T. J. Kitchings. 1975. "The Availability of 137C s to Fishes from Ingested Clays." Verh. Internat. Verein. Limnol. 19:

2504-2509.

l Gabelhonse , D. W. , Jr. 1984. "A Length-categorization System to Assess Fish Stocks. " N. Am. J. Fish. Maname. 4:273-285.

i International Commission on Radiological Protection. 1977.

" Recommendations of the International Commission on Radiological Protection, ICRP Publication 26. " Ann. ICRP 1(3):2-47, Pergamon Press, Oxford.

Kolehmainen, S. E. and D. J. Nelson. 1969. The Balances of 137pt, l

i Stable Casina. and the Feedina Rates of Blnealli (Lemonta_

ascrochirns Raf.) in White Oak Lake. ORNL-4445, Oak Ridge National Laboratory, Oak Ridge, Tennessee, p. 114.

SS l

I L . . _ . - . . . - - . _ _ _ - - . _ _ _ . _ _ _ _ _ , . _ _ . .

56 Miller, C. W. and F. O. Hof fman.1983. " An Examisation of the Environmental Half-time for Radionuclides Deposited on Vegetation."

Realth Physics 45 (3):731-744.

Pendleton, R. C. and W. C. Hanson. 1958. " Absorption of Cesium-137 by Components of an Aquatic Community. " In: Prce.. Second Interational Conf. on Peaceful Uses of Atomic Emerar. United Nations, Geneva, Switzerland, pp. 419-422.

P1fleger, W. L. 1975. The Fishes of Missouri. Missouri Department of Conservation, Jef ferson City, Missouri, p. 343.

Rupp, E. M. 1984. " Adul t Die tary Intake and Inhalation Rates. " In:

Models and Parameters for Environmental Radf olonical Assessment s, (Miller , C. W. ed.), DOE / TIC-11468. DOE Critical Review Series, Technical Information Center, U.S. Departnest of Energy, Oak Ridge.

Tennessee, pp. 55-56.

Snedecor, G. W., and W. G. Cochran. 1967. lis t in t ic al Me thod s , Sixth Edition. Iowa State University Press, Ames, Iowa, p. 593.

U.S. Environmental Protection Agency. 1976. ladioloalcal Quality of thi Environment. EPA-520/1-76-010, Office of Radiation Progrens.

Washington, DC.

' U.S. Environmental Protection Agency. 1977. 40 CFR Part 190,

- Environmental Radiation Protection Standards for Naclear Power Operations." Fed. Remist. 42(9):2858-2861.

U.S. Nuclear Regulatory Commission. 1977. . Calculation of A==nal Doge 1_

12 Man from Routine Releases of Reactor Effluents for the Purnose of Evaluatina Come11ance with 10 CFR Part 50 Annendix I (Revision 1).

Regulatory Guide 1.109, Office of Standards Development, Washington, DC.

United Nations Scientific Committee on the Effects of Atomic Radiation.

1982. Ionizian Radiation: Sources and 31oloalcal Effects. United Nations, New York, N.Y.

. Vanderploeg, H. A., D. C. Parzyck, W. H. Wilcox, J. R. Kercher, and S. V. Kaye. 1975. Bloacenanlation Factors for Radionuclides in Freshwater Blota. ORNL-5002, Oak Ridge National Laboratory Oak Ridge, Tenne s see , p. 222.

Van Winkle, W. , R. W. Counts, J. G. Dorsey, J. W. Elwood, V. W. Love ,

Jr. , R. McE1haney, S. D. Schlotzhauer, F. G. Taylor, Jr. , and R. R.

Turner. 1984. Mercury Contaminat f or. in East Fork Ponlar Creek and Bear Creek. ORNL/TM-8894, Oak Ridge National Laboratory Oak Ridge, Tennessee, p. 72.

j I

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APPENDII A CON GNIltATIONS OF RADIONUCLIDES IN ENVIRONMENTAL SAMPLES t

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Table A-1. Concentrations of radionuclides in California background soil samples Concentrationa .b of radionuclide (pCi/g, dry weight)

Sampl e numberc 137Cs 134Cs 60Co 58Co 54Mn 226Ra 23 8gd 232Th 40K CA4 0.7910.19 (0.1 (0.11 (0.13 (0.09 1.4 1 0.21 1.07 1.5 f 0.63 27 f 2.6 CAS 1.330.12 0.0710.08 (0.07 (0.08 (0.06 1.1 1 0.17 1.13 1.2 f 0.5 9 1911.6 CA6 0.02 f 0.04 0.03 f 0.04 (0.03 (0.04 (0.03 0.9810.13 0.92 1.0 f 0.33 1710.86 CA7 0.61 + 0.0 8 0.06 + 0.0 8 (0.05 (0.05 (0.04 1.1 + 0. 22 1.28 1. 5 f 0. 5 9 2.110.69 4

CA8 0.33 + 0.0 9 (0.05 (0.06 (0.07 (0.05 0.73 + 0.14 G.77 0.63 + 0.21 12 + 1. 5 CA9 0.23 2 0.05 0.05 f 0.09 (0.03 (0.04 (0.03 0.55 1 0.11 0.49 0.46 f 0.19 9.7 1 0.67 h CA10 0.26 f 0.99 (0.06 (0.06 (0.08 (0.05 0.5510.09 0.46 0.47 f 0.3 9 9.5 1 1.2 Call 0.07 2 0.05 0.03 1 0.03 (0.03 (0.04 (0.03 0.7 8 f 0.13 0.68 0.74 2 0.17 13 1 0.76 CA12 0.89 2 0.15 (0.03 (0.04 (0.04 (0.03 0. 89 f 0.15 0.73 1.13 f 0.40 23 1 0.94 CA13 0.1130.05 0.07 f 0.12 (0.03 (0.04 (0.03 1.16 2 0.13 0.56 0.8210.29 1410.82 CA14 0.2 9 f 0.09 (0.06 (0.06 (0.07 (0.05 0.65 1 0.04 0.53 0.76 1 0.46 23 1 1.5 CAIS (0.04 (0.03 (0.04 (0.05 (0.03 0.40 + 0.07 0.37 0.7810.37 3521.0 aIndicated counting error is at the 95% confidence level (f 2a).

b Concentration values preceded by ( are below the minimum detectable amounts (MDA).

CFor location see Fig. A-1.

dErrors associated with 2380 concentrations are f 5% (2a).

m*

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Toble A-2 (sentlemed)

Cescentratione .b of redieneelide (pfils, dry weight)

Sempte Depth member * (ie.) 337Ce 334Ce ecc . S tre $43 , 2263 , 238, 233Th 40g u tid _11 RSS072A 0-2 0.3020.05 0.06 3 0.03 (0.03 (0.03 (0.02 0.7930.08 -

0.71 2 0.23 15 3 0.79 R550734 0-2 0.38 3 0.07 (0.04 (0.05 RS50734 6-2 15 3 0.39 (0.04 (0.04 0.90 f 0.Il -

0.7830.32 14 2 1.0 5 3 0.$3 2.2 3 0.30 (0,10 0.30 + 0.10 0.9830.16 -

O.8330.20- 13 31.5 utid_Li RSS0734 6-3 (0.06 (0.04 (0.05 (0.05 (0.04 1.0 2 + 0.2 3S50794 0-4 (0.71 0.84 3 0.43 8.6 3 0.93 (0.04 (0.04 (0.04 (0.03 0.4830.00 -

0.3530.13 4.7 2 0.83

• Indireted seesties errer is et the 9M confidence leest (2 2e).

bremsentrattee selees preceded by ( are belee the eletous detectable oneset (WA).

'For lece t tee see Fige. 2-6.

C

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Totte A-3. Ceasestrettese of re40esett teos te vegesettee semplee Cemeenteettesa .b ,g ,,gg, gg4e (pCI/kg. see seteht3 Sempt e embe rs 137c, 134c, etc. S tc, 34g, n ote, 144c, 89g, Seg, 7, 3 4eg Integ g 1313 E1eldJ asvee? Stee + 279 22:4 + ISS 72.9 3 1 e. 8 -

15.7 + 5.4 (II 454 <270 <278 2Me ; 279 1971 3 I se -

< s.1 asvees 324e 2 279 s t e? 2 85 St.3 3 8.1 -

26 + S.4 (13 (54 <270 (278 - 2376 3 1 89 263 9 3 t ot -

( 5. 4 astett 2376 ? 162 1953 ; SR 4e.S 2 2.7 - - - - - - - - - -

asvet! 178I 2 tot . 479 + S4 8.3 3 e.st - - - - - - - - - -

asvets 19 ! 1.9 427 <27 - - - - - - - - - -

asves t 70 m S.4 427 (27 - - -- - - - - - - -

EteldJ aste3e 2295 ; 335 st ee 3 m 93 3 S.4 - - - - - - - - - -

one24 346 s.t 59e ; $4 24 3 2.43 - - - - - - - - - -

EJeldJ aste27 2ee 13.5 tie ; s. <27 - - - - - - - - - -

asvese (27 <27 (27 - - - - - - - - - -

asve3 <27 <27 <27 - - - - - - - - - -

Eleid_9 asve33 2e19 ; 135 736 3 54 4e.5 3 S.4 - - - - - - - - - -

asve34 aft + 16.2 13 5 + s.1 (27 - - - - - - - - - -

EisidJ asses e 163 3 at 7e ! S.4 <27 - - - - - - - - - -

Eteld_f asveSt (27 <27 <27 - - - - - - - - - -

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Toble a-3 feesttened) ceasesteettees .b et seateneestae fpct/te. eet eeteht)

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'ledtseted seestles esses to et the est esef teesse f eeel (! 2st.

b Ceeseetsottee selees preceded by < ere below the stateam detestable eseest (24 ) .

' Fee losettee see Ftse. 2-4.

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Table A-S. Concentrattens of redlemaclides la water samples Conce nt r a t i on a .b g ,,4 g o. ,3 g g, g,cg f L)

Grose Semple 895, 24c 231I sty 6e saber

• 137Cs 1340s 60c, 58u 14t c, 144c, M5r 3R (2.7 314 70.200 1 2.700 ($10 (2.7 32.4 1 $7 395001 (2.7 (1.9 (2.7 (2.7 (2.7 (8.1 (1.9 (2.7 (2.7 (5.4 1.6 1 3.8 9,720 1 1.350 (810 (2.7 16.2 1 24 355005 (2.2 (2.2 (2.7 eindicated constins error is et the 95% confidence level (12e).

bValues indicated are less then staleam detectable esosat s (NDA).

cFor location see Fiss. 2. 6. and 7.

ad

68 Table A-6. Concentration of radionuclides in arist muscle of fish collected at various sites downstream of the Rancho Seco Nuclear Power Plant, December 1984 Total Standard Concentration Weight (pC1/3, wet vt)

Site Species Sez" 1ength length g)

(ca) (ca) 137Cs 134Cs 60Co Clay Green N 17.4 14.8 101.1 12.02 5.66 0.48 Creek sanfish U 16.8 14.2 89.7 D

9.17 4.20 0.59 (Lenomis F 15.2 12.8 66.3 8.89 4.48 (0.06 cyane11us)

Largemouth ND 27.5 22.9 384.2 8.17 3.28 0.54 bass ND 25.1 20.5 283.4 10.70 4.84 0.34 (Micronterns ND 17.4 14.3 69.4 8.02 4.10 0.38 salmoides)

Black U 32.7 28.3 464.1* 6.33 2.50 0.79 bullhead U 17.8 14.8 64.4* 7.53 3.81 0.23 (Ictainens U 17.0 14.5 60.5* 7.63 4.48 (0.07 nelas)

Badselville Green N 18.5 16.1 129.2 D

10.48 4.60 0.41 Creek santish F 15.8 13.4 75.8 3.87 2.54 (0.06 b

N 14.1 13.4 75.8 5.38 2.26 0.40 Black U 28.0 23.6 266.8* 9.80 3.97 0.55 bullhead U 26.8 23.2 253.3* 10.40 5.15 0.38 U 23.0 19.8 156.3* 7.43 4.10 0.40 Laguna Green N 14.9 12.5 71.3 0.81 0.66 (0.05 Creek at sunfish N 15.0 12.3 69.4 0.84 0.12 0.48 Laguna Rd F 12.3 10.2 38.2 0.36 0.06 0.30 Black F 21.9 17.5 163.0 1.46 0.70 0.35 crappie M 19.5 15.4 115.2 1.28 0.71 (0.04 (Pomozis F 14.5 11.1 40.3 2.00 0.92 0.06 ninromaculatus)

69 Table A-6 (continued)

Total Standard Concentration Site Species Sen* Weight (pC1/s, wet vt) 1essth length

(**) (**) 137Cs 134Cs 60Co Black U 15.7 13.4 50.8 0.09 (0.05 0.23 ballhead Dry Creek #

Green M 16.3 13.9 85.4 (0.06 0.27 0.05 (control) sanfish M 15.2 12.4 62.1, (0.05 0.05 0.60 d

M 12.3 60.6 0.05 0.05 0.66 "F = female; M = male; U = maknown; ND = not deteralsed.

Estimated ty: los10W (fish weight in s) = -1.3953 + 2.9055 log 10L (standard length in cm), r2 = 1.00 and a = 26.

' Estimated by: log 10W (fish weight in g) = -1.7577 + 3.0475 log 10L (standard length in cm), r 2 = 0.99 and a = 20.

Estimated by: log 10W (fish weight in 3) = -1.4208 + 2.93 90 log 10L (standard length in co', r2 = 1.00 and n = 8.

19 Table A-7. Concentration of radicanclides in axial muscle of fish collected from three small ponds near the Rancho Seco Nuclear Power Plant Concentration Total Standard Weight (pCi/g, wet vt)

Site Species Sez' tength length

(*") (**) 137Cs 134Cs 60Co b 11.10 5.77 <0.05 Samp Blue gill F 15.0 12.5 70.7 (Lesomis M 16.2 b 13.1 83.8 6.50 2.96 0.08 nacrochirus) U 16.2 b 13.2 89.2 5.76 3.09 (0.04 F 16.7 13.1 76.9 6.85 3.07 (0.05 U 18.4 D 14.6 148.6 5.72 2.55 (0.04 F 18.5 15.0 130.9 6.02 2.90 (0.04 F 21.1 16.8 192.7 4.87 2.40 (0.05 M 14.4 11.6 61.8* 3.94 1.51 0.59 E

Largemouth M 39.0 33.5 1,120.0 14.42 7.19 0.40 bass F 33.4 27.2 583.6 6. .6 0.53 d

(Micronterns M 29.3 24.3 410.2 14.44 6.14 0.57 malmoldes)

~

Black M 27.9 23.6 266.8' 6.47 2.88 0.37 D

bullhead F 23.2 19.5 146.8 8.87 4.33 <0.04 (Ictalurus U 20.0 17.2 101.8' 3.54 1.91 0.14 melas)

Pond 1 Bluegill F 21.0 16.6 176.9 0.26 (0.05 0.61 F 18.7 14.5 143.0 0.14 (0.05 0.52 F 17.5 13.5 91.6 0.66 (0.06 0.66 Largemouth F 38.8 31.2 886.9 0.24 0.06 (0.03 bass F 36.2 30.0 687.1 0.13 0.10 0.19 M 35.8 29.5 785.3 0.13 <0.03 0.40 Pond 2 Green U 11.5 9.5 34.1 <0.06 0.32 0.11 sunfish U 10.8 8.8 28.7 0.21 <0.07 0.21 (L9somis U 9.6 7.8 18.9 0.81 <0.11 0.61 cyanellus)

71 Table A-7 (continued)

Concentration Total ~8tandard (pci/s, wet vt)

Weisht Site Species Sex" length length g)

(*") (**) 137Cs 134Cs 60Co 33.0 27.8 754.6 4.48 1.90 0.27 Largemouth N 25.7 21.2 263.8 3.52 1.76 0.14 bass F 25.5 21.2 264.6 1.48 0.34 0.31 N

19.0 162.2 0.78 (0.06 0.55 Black U 22.5 15.8 92.9 0.71 0.06 0.58 bullhead U 18.6 11.9 35.1 1.25 1.11 0.34 U 14.1 "F = female; M = male; U = unknown.

Fish collected on November 14, 1984; all other fish were collected on December 10-12, 1984.

• Estimated by: log 10W (fish weight in 3) = -1.4773 + 3.0704 log 10L (standard length in cm), r2 = 1.00 and a = 21.

Estimated by: log 10W (fish weight in ) = -1.7219 + 3.1285 log 10L (standard length in cm), r 2 = 1.00 and a = 17.

' Estimated by: log 10W (fish weight in g) = -1.7577 + 3.0475 log 10L (standard length in cm), r2 = 1.00 and a = 20.

12 Table A-8. Concentration of radionuclides in axial muscle of frogs from two sites near the Rancho Seco Nuclear Power Plant. December 1984 Concentration a Weight (pC1/3, fresh vt)

Site Species (s) 137Cs 134Cs 60Co Pond 1 ballfrog 292.8 0.06 (0.04 0.25 (Rama catenbeiana)

Lagasa Creek ND 98.7 (0.06 0.11 0.27 near McKenzie ND 37.3 0.23 (0.08 0.31 Road "ND = no t de t e rmine d.

73 Table A-9. Concentration of radionuclides in axial muscle of game birds collected at several sites near the Rancho Seco Nuclear Power Plant, December 9 and 13, 1984 Concentration a Weight Collection (pci/s, wet vt)

Species Sex (g) site 137Cs 134Cs 60Co American ND 539 Samp (0.08 0.08 1.21 coot (Felica --=ricana)

American ND 588 Pond 1 (0.07 0.27 0.14 coot Wilson's ND 1017 Clay Creek (0.07 0.13 0.33 snipe near SNUD (Canella bonadery delicata)

American ND 630 Clay Creek 0.95 0.42 0.42 b

bitttern west of Rte 104 (Botaurus laatialmosus)

Pheasant M 1010 Field just north 0.31 (0.07 0.68 (Phasiaans of Clay Creek and 121chicus) west of Rte 104 Pheasant M 967 Field just south 0.21 (0.06 0.21 of Clay Creek and east of Ete 104

'N = male; ND = not determined.

b Not a game bird; species was collected because its diet, although varied, consists of small fish (Bent 1926).

5 O

APPENDIX B QUALITY Cormt0L PROCEDURES l5 si i

77 The radiological survey and analyses of environmental samples from the Rancho beco Nuclear Power Plant environs was carried out withis the general guidelines of Oak Ridge National Laboratory Quality Assarance Procedures.

The redischemical analyses of environmental samples pe rf ormed by the Analytical Chemistry Division were carried oat within the controls provided by the division's Quality Assurance Program (copy attached).

In accordance with this program, the analytical laboratories withis the division submit quarterly quality-control reports to the division Quality Control Coordinator. The Rancho Seco environmental samples were analyzed by the low-level analytical laboratory of the Analytican Chemistry Division. The control results from this laboratory for the fourth quarter of 1984, covering the time in which Rancho Seco samples were analyzed, is attached.

Portable instruments used in the field to measure gamma radiation levels are calibrated at six-week intevals in the calibration facility i

of the Environmental and Occupational Safety Division of Oak Ridge National Laboratory. The sources used are National Bureau of Standards (NBS) or are traceable to NBS standards. In addition, each portable ins t r ume nt is checked in the fleid daily for proper operation using uranium check sources.

High resolution gamma spectrometry instraments (GeLI) used by the Radiological Survey Activities (RASA) group of the Health and Safety Research Division (HASRD) to assay environmental samples are calibrated routinely using NBS traceable sources. In addition, a number of samples are routinely submitted to other counting facilities within ORNL for independent assay. Table B-1 gives the results of a group of Rancho Seco samples that were analyzed by two ladependent countlas facilities.

For the aquatic sampling program, the Environmental Sc ience s Division used a NaI(T1) gemas spectrometry system. Duplicate samples were taken from eight of the 52 fish (15%) collected in December and submitted to the Analytical Chemistry Division also for analyses. All samples were analyzed for 137Cs, 134Cs, and 60C o and scanned for other gamma ray-enaitting radionuclides by the Analytical Chemistry Division using a GeLi detector. Table B-2 gives the results of these two ladopendent concentration measurements.

Table B-1. Camperison of samma spectremetry resalts of soil semple smalyses performed by too ladependent laboratories Concestration of redlemaclide (pCi/s. dry wel ht) 337c, 33ks 8%e 3Co 34Na Sample sember RASA* ACb gggae Act RASAs Acb RASAs Ach RASAs ACb RS$001 7.7 + 0.20 7.7 1.7 3 0.21 1.7 4. 9 + 0.2 5 4.6 ( 0.0 98 -

0.33 + 0.09 0.37 RS$0024 33 + 0. 84 34 13 3 0.91 12 6.0 f 0.03 5.7 1.4 + 0.3 2 0.37 0.64 2 0.27 0.63 155006 1230.41 13 4.9 + 0.6 5 4.5 1.4 + 0.0 5 1.4 (16e 0.07 0.22 + 0.12 0.24 RSS007 22 + 0.36 22 7.3 + 0.95 6.7 2.7 + 0.21 2.5 (15c -

0.4920.11 0.50 19550018 15531.7 140 6534.9 57 29 + 2.2 26 16 + 0.60 14 4.6 + 0.48 3.8 3S55002 0.26 3 0.06 0.26 0.15 3 0.03 0.13 (0.04c - <o,04c . <o,oje _

RSW5006f 115 3 1.6 100 45 3 3.2 40 13 2 1.6 11 3.4 3 0.46 3.2 1.4 3 0.37 1.4 g 8Amalyses performed la the Radiological Servey Activities (RASL) Croep coastlag f acility at Ook Ridge Nationel Laboratory. Errors associated with these concentrations are 2e (99% confidence level).

D Amelyses performed by the Analytical Chemistry Divistem of Ook Ridge Nettomat Laboratory. The overall ascerteisty la the concentrations of major constitseat s is ! !OL (2e); the ascertainty of staar constitaent s is of the order of f 25%.

cConcentrations are less thee the stateam detectable amoest (ISA).

d11th'Ag - 4.8 pCi/s.

eIIO*Ag - 1.3 pct /s.

(110 bag - 0.66 pct /s.

79 Table B-2. Comparison of radionuclide concentrations in duplicate tissue samples analyzed by the Environmental Sciences Diviolon, and in parentheses with 95% confidence int e rval, the Analytical Cheatstry Diviolom Sample Sample Sample Concentration (pci/s)

Number Description Location se'Cs as*Cs **Co 1 Coot Sump (0.08 0.08 1.21

((0.19) (<0.14) (<0.16) 2 Pheasant Hadselville 0.21 (0.06 0.21 Creek (<0.11) (<0.11) (<0.11) 3 Black Laguna Cr. at 0.84 0.35 0.53 bullhead Laguna Rd. (0.92 1 0.22) (0.3810.16) ((0.11) 4 Frog Pond 1 0.06 (0.04 0.25

(<0.08) ((0.05) (<0.08) 5 Largenouth Pond 1 0.24 0.06 (0.03 bass (0.32) (<0.08) (<0.11) 6 Largenouth Sump 16.75 7.76 0.53 bass (17.82 1 1.08) (6.75 1 0.54) (<0.11) 7 Black Clay Creek 6.33 2.50 0.79 bullhead (7.29 1 0.54) (2.56 1 0.27) (0.12 1 0.10) 8 Green Dry Creek (0.06 0.27 0.05 sunfish ((0.08) (<0.08) (<0.08)

-oAx 3 ames '

NA7iOMAL -

tasonarony. -

l QUALITY 7' g:: 7 ASSURANCE PROGRAM F N 1 <

l ANALYTICAL

~

CHEMISTRY DIVISION

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$1 OVALITY ASSURANCE PROCEDURE OAK RIDGE N ATIONAL LABORATORY " ' O A- AC D- 1 8-1-83 QUALITY ASSURANCE PROGRAM ..

3 ,, 3

, ... ,.., ~ .. .c TITLE:

ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM POLICY STATEMENT in accordance with the Quality Assurance Program goals established by the Director of the Oak Ridge National Laboratory (0RNL), it is the policy of the Analytical Chemistry Division (ACD) to establish, nain-tain, and enforce an ef fective quality assurance program. This effort is designed to meet the requirements of the ORNL Quality Assurance Program and has been prepared to be consistent with the applicable parts of the following documents: DOE Order 5700.6, ANSI NQA-1, and the ORNL QA program.

The work of the Analytical Chemistry Division includes basic research, applied research, development and support activities, it is the policy of the Analytical Chemistry Division to maintain a quality assurance program that will aid in ensuring reliable results and in the efficient and safe operation of all facilities used by members of the division.

The Director of the Analytical Chemistry Division has responsi-bility for the execution of the Quality Assurance Program defined here.

The ACD Quality Assurance Coordinator is responsible for preparation of this Quality Assurance Program Manual. The ACD managers are responsible for implementation of the Quality Assurance Program with assistance from the Quality Assurance Coordinator. All staff nenbers are responsible for applying the appropriate quality assurance procedures in their work. Implementation of the Quality Assurance Program will be checked periodically by the Division Director through audits conducted by the Quality Assurance Coordinator.

t OAK RIDGE NATIONAL LABORATORY o...no..

UNION CAR 81DE CORPOR ATION hu(itat Divi 5 04

s2 j OVALITY ASSURANCE PROCEDURE OAK RIDGE N ATIONAL LABORATORY " ' OA-ACD-1

's QUALITY ASSURANCE PROGRAM 2 1u 5 TITLE:

ANALYTICAL CHEMISTRY DIVISION OVALITY ASSURANCE PROGRAM

1. Mission of the Division The Analytical Chemi s t ry Livision (ACD) engages in research, development, and support activities in analytical chemistry science. The mission of the division is threefold: (1) to provide analytical expertise in support of Laboratory programs, (2) to con-ceptualize, develop, and carryout R/D programs that are analytical in nature, and (3) to provide high quality analytical ~ chemistry support services.

2. Conduct of Division Activities 2.1 Research/Developnent Programs The R/D programs in ACD are planned activities with stated objectives. The work is performed by a group of professional scientists and a small number of trained technicians under the direction of a group or task leader. The experiments progress stepwise so that failure at one point does not threaten the p rogram. Controls fall into three areas: (1) peer review in either formal or informal meetings, (2) mandated quality assurance l actions by the sponsoring agency, and (3) internal and external audits.

2.2 Support Programs These programs encompass the more routine analytical measurements performed in support of Laboratory projects or work for others.

The work is performed by professional scientists and trained technicians under the direction of a group or task leader. The tests performed are part of a larger progran and as such do not constitute a large risk to failure. Controls fall into four areas:

(1) quality control sanples prepared by ACD to be similar to process samples, (2). standard reference materials prepared by recogized authorities such as the National Bureau of Standards and USDOE New Brunswick Laboratory, (3) controls prepared to simulate process material, and (4) internal and external audits.

OAK RIDGE NATIONAL LABORATORY UNION CAR 8lDE CORPOR Afl0N

.. Approved By: O- -

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63 OAK RIDGE NATIONAL LABORATORY QUAW ASSWEE NCEDWE

""'"" OA.ACD-1 QUALITY ASSURANCE PROGRAM ~

2 c. s TITLE: ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM Responsibilities 3.

3.1 The Division Director 3.1.1 Appoints a division Quality Assurance Coordinator (QAC).

3.1.2 Authorizes preparation of documents related to quality assurance when appropriate.

3.1.3 Implements QA procedures within the division.

3.1.4 Provides the division QAC information on new projects.

3.2 The Division Quality Assurance Coordinator 3.2.1 Coordinates and assists in the preparation of quality assurance related documents.

3.2.2 Arranges for review and approval of appropriate docu-ments by the Division Director and the ORNL Quality Assurance Program Director.

3.2.3 Infcrms the Division Director of Quality Assurance activities within the division.

3.2.4 Maintains a file of ORNL and division QA procedures, ORNL Master Analytical Methods, Quality Assurance Assessments (QAA) and plans, quality failu e and audit reports.

3.2.5 Reviews and approves division QA assessments and QA l plans.

i 3.2.6 Performs internal audits and assists others in perform-ing audits.

l

! 3.2.7 Interprets quality assurance procedures for the division.

3.2.8 Produces an annual report of QA actions.

I e

?l "'*.' , .

S4 A ASS ANCE NCEME OAK RIDGE NATIONAL LABORATORY P40CLovat ns.

OA'ACD-1 QUALITY ASSURANCE PROGRAM ~

3 e, s TITLE: ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM 3.3 Section Head 3.3.1 Implements QA procedures within the section.

3.3.2 Reviews ar:d approves section QA plans.

3.3.3 Reviews Group / Task Leader actions to ensure that these responsibilities are discharged.

3.4 Group / Task Leader 3.4.1 Plans the R/D or support program for the group assisted by the scientists involved.

3.4.2 Prepares needed Quality Assurance Assessments, Plans, and Procedures for these programs.

3.4.3 Informs the QAC of any new programs, procedures, or equipment not covered by existing QAAs.

3.4.4 Bears responsibility for the quality assurance of the p rog ram.

3.4.5 Initiates a Quality Investigation Report (QlR) in the

event of any significant failure occurring during operations.

4. Quality Assurance Education Each employee of the Analytical Chemistry Division will be informed of the purpose, need, and scope of this Quality Assurance Program.

Orientation sessions by the QAC will be provided to inform new l employees of their roles in providing assurance of quality. The l QAC will make periodic reports to ACD supervisory personnel on cur-rent QA procedures and directions. The division will comply with l guidelines described in QA-L-1-102 and participate in activities such as QA week and video tape presentations.

, %eT95

SS OAK RIDGE NATIONAL LABORATORY ,.ouoo. o.

QUALITY ASSURANCE PROGRAM 4 c- 5 M E: ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM

5. Implementation 5.1 This program is to be used as a supplement to the Laboratory's Quality Assurance Manual. No part of this document supersedes nor may be used as a substitute for those requirements given in UCC-ND SPP D-2-16, ORNL Supplement to D-2-16 and the ORNL Quality Assurance Manual.

5.2 A QA Assessment shall be completed for all projects to identi fy and evaluate the risk of potential significant quality problems (failure modes), and for each quality problem with an acceptable ri sk provide a rationale for the determination. For each potential quality problem with an unacceptable risk, define the planned preventative action (s) required to provide confidence that the problem is unlikely to occur or to minimize the consequences of the problem if it does occur, and to specify the responsibility and schedule for carrying out the preventative actions (s). ORNL QA procedure L-1-103 (Rev. 8), provides guidance in this evaluation.

5.3 For all prograns and activities the Group / Task leader will be responsible for application of the following elements in order to meet quality assurance requirements.

5.3.1 All ACD and ORNL quality related standard practice procedure and nanuals shall be observed.

5.3.2 UCCND Standard Practice Procedure D-5-5 and ORNL QA procedure QA-L-3-100 (Rev. 3) shall be observed in recording research/ development data and in document  !

control.

5.3.3 All laboratory equipment and instruments shall be identified, calibrated peri.odically and appropriate records shall be maintained. ORNL QA-L-14-100 (Rev. 3) describes these requirements. Those instruments from which reportable data is obtained_ are of particular i mportance.

l 5.3.4 Results of research shall be published in ORNL docu- '

ments, and in scientific jou rnal s , and presented at scientific meetings when appropriate.

l l ' Y.""*;*!',

86

^

^ ^

OAK RIDGE NATIONAL LABORATORY ..o u ce. .o.

~

QUALITY ASSURANCE PROGRAM 5 c- 5 )

l I

TITLE: ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM 5.3.5 Any significant changes in the program or activity shall be discussed with the QAC to determine whether additional quality assurance procedures should be implemented.

5.3.6 All significant quality problens shall be investigated, i documented for management review and, when appropriate, corrective action taken. QA-L-6-101 (Rev. 3) describes these procedures and references the needed QA proce-dures for quality investigation reports, ncnconforming itens and others.

5.3.7 The retention and disposition of quality related records shall follow the procedures described in 0A-t-16-100.

5.3.8 Purchase of standard and special itens sh311 be accomplished in a manner to ensure adequate quality.

0A-L-9-100 (Rev. 2) describes these procedures and references appropriate QA procedures for procurement, inspection, quality problems and others, r/ ~-':.',',',

81 OAK RIDGE NATIONAL Analytical Chemistry i - - - - -

Division

General anti Environmental l Analysis Section 1

Quarterly Quality Control -

Report October-December 1984 (PERATED BY MARTIN MARIETTA ENERGY SYSTEMS INC.

FOR THE UNUED STATES DRARTMENT OF ENERGY

88 INTRA-LABORATORY CORRESPONDENCE OAK RIDGE NATICNAL LABORATORY -

January 11, 1985

-To: T. G. Scott, low Level Radiochemical Analytical Laboratory From: P. L. Howell, Quality Control Coordinator

Subject:

Control Results for Fourth Quarter 1984 CONTROL RESULTS FOR 4T!! QU ART ER 1984 LAE:45003-NUM LIMIT NUM.

OF OF 257. CALC OUT BIAS 1ETHOD: DET ER :CCOD E TESTS ERROR ECUND 'T'  % BIAS CNTRL SIGNIF

HEM S3 P

S R-90 :RSRYS 11 +15.00 + 18. 005 -0.2180 -0.62 1 NO I-SPEC:Co-60:RCC5: 14 +8.00 +3.176 + 2.152 8 +0.9 2 0 NO 12 +6.00 +1.407 + 8. 718 3 +1.80 0 YES i-5 P EC: CS- 137 : ECC S:

LIQ SCINT:H-3:RTR IB: 3 +10.00 +0.036 +247.4358 +2.70 0 YES 40 T Quality level = No. results in control x 100 Total No. results Quality level for the Low level Radiochemical Analysis Laboratory for 4th quarter 1984 was 98%.

cc: W. R. Laing D. A. Lee l

R. K. Owenby l L. M. Roseberry J. R. Stokely (2) b ..

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APPENDIX C RELEASE DATA 1

1 1

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95 l l

Table C-1. Liquid effluent releases (C1) from the Rancho Seco Nuclear Power Plant [SMUD (1985)]

Nuclide 1980 1981 1982 1983 1984 3

H 1.47 E-02a 8.35 E+01 6.46 E+01 7.43 E+01 2.97 B+02 Na 0 0 1.40 E-04 4.15 E-04 5.95 E-04 1

Cr 0 0 6.71 E-03 0 -

54 Mn 0 4.22 E-02 1.05 E-02 5.13 E-03 2.45 E-03

'Fe 0 3.92 E-04 2.32 E-03 0 0 Co 0 1.47 E-04 0 0 0 8

Co 0 3.04 E-01 1.26 E-01 3.22 E-02 1.13 E-02

' Co 0 6.09 E-02 2.21 E-02 1.53 E-02 1.94 E-02

' Zr 0 4.53 E-03 2.15 E-03 0 1.26 E-04 I O 3.47.E-02 1.58 E-02 3.67 E-02 1.23 E-01 I O 4.70 E-03 1.3 9 E-03 6.88 E-04 1.71 E-02 135 I O O 1.27 E-04 1.77 E-03 1.87 E-03 14 Cs 1.34 E-03 4.95 E-02 9.61 E-03 6.99 E-02 1.53 E-01 Cs 0 0 3.07 E-04 1.71 E-03 4.28 E-03 Cs 2.43 E-03 8.92 E-02 1.87 E-02 1.16 E-01 3.01 E-01 110m Ag- 0 6.34 E-04 1.25 E-05 0 1.45 E-03

" Ba 0 1.36 E-02 1.26 E-04 0 0 Sr 0 0 0 1.08 E-03 0 133 Xe 0 0 3.81 E-04 0 3.39 E-02 135 l

1e 0 0 1.62 E-04 0 4.97 E-03 i

I "1.47 E-02 = 1.47 x 10-2

• --v- - - - w -

M REFERENCE Sacramento Municipal Utility District. 1985. Radiation Emnosare.

Environmental Protection Effinent and Waste Disnosal. Jannary-December 1984 Annual Renort. Rancho Seco Nnclear Generatina Station Unit No. 1. Clav Station. California. License N- ker DPR-54.

i

u 95 Table C-1. Liquid effluent releases (Ci) from the Rancho Seco Nuclear Power Plant [SIRTD (1985)]

Nuclide 1980 1981 1982 1983 1984 H 1.47 E-02 8 8.35 E+01 6.46 E+01 7.43 E+01 2.97 B+02 Na 0 0 1.40 E-04 4.lf *! 04 5.95 E-04 Cr 0 0 6.71 E-03 0 -

Mn 0 4.22 E-02 1.05 E-02 5.13 E-03 2.45 E-03

'Fe 0 3.92 E 2.32 E-03 0 0 Co 0 1.47 E-04 0 0 0 Co 0 3.04 E-01 1.26 E-01 3.22 E-02 1.13 E-02 Co 0 6.09 E-02 2.21 E-02 1.53 E-02 1.94 E-02

' Zr 0 4.53 E-03 2.15 E-03 0 1.26 E-04 II I O 3.47 E-02 1.58 E-02 3.67 E-02 1.2'3 E-01 I O 4.70 E-03 1.39 E-03 6.88 E-04 1.71 E-02 135 I O O 1.27 E-04 1.77 E-03 1.87 E-03 134 Cs 1.34 E-03 4.95 E-02 9.61 E-03 6.99 E-02 1.53 E-01

'Cs 0 0 3.07 E-04 1.71 E-03 4.28 E-03 Cs 2.43 E-03 8.92 E-02 1.87 E-02 1.16 E-01 3.01 E-01 "As 0 6.34 E-04 1.25 E-05 0 1.45 E-03 Ba 0 1.36 E-02 1.26 E-04 0 0 Sr 0 0 0 1.08 E-03 0 133 Xe 0 0 3.81 E-04 0 3.39 E-02 I 'Xe 0 0 1.62 E-04 0 4.97 E-03

• 1.47 E-02 = 1.47 x 10-2 1

M REFERENCE Sacramento Municipal Utility District. 1985. Radiation Exnosure.

Environmental Protection Effluent and Was t e Discosal. J anuary-December 1984 Annual Renort. Rancho Seco Nuclear Generat a== Sta tion Unit No. 1. Clav Station. California. License "- 'er DPR-54, 1

l

9 9 g paTic1PAhTS D

/

99 The authors of this report have been the Principal Investigators on this project. However, there were . many other pe rsons t ho made significant contributicas to this project. Listed below are some of these additional persons and the area in which they contributed to this proj ec t.

Field Sa= ale Collection D. E. Cox - Environmental Sciences Division, ORNL W. C. Kyker - Environmental Sciences Division, ORNL J. L. Malone - Environmental and Occupational Safety Division, ORNL B. Millar - Private Consultant, Colusa, California J. A. Roberta - Health and Safety Research Division, ORNL W. H. Shinpaugh - Health and Safety Research Division, ORNL Sa=nle Prenaration and Analysis A. C. Butler - Health and Safety Research Division, ORNL B. S. Ellis - Health and Safety Research Division, ORNL J. S. Eldridge - Analytical Chemistry Division, ORNL J. F. Emery - Analytical Chemistry Division, ORNL M. L. Frank - Environmental Sciences Division, ORNL G. A. Moore - Operations Division, ORNL S. W. Nichols - Environmental and Occupational Safety Division, ORNL T. G. Scott - Analytical Chemistry Division, ORNL This proj ect could not have been brought to a timely and successful completion without the contributions of these persons.

I I

APPENDIX E RADIATION UNITS USED IN TEIS REPORT

198 The radiation doses and exposures presented in this report are given in terms of older units rather than in terms of the International System of Units (SI). Given below is a table which contains the relations between the various radiation quantities in each system. This table is provided to assist the reader in converting from one se t of units to the other.

New SI Quantity unit and Basic SI Old nai6 Conversion symbol dimensions and symbol Exposure coulomb rootsen (R) 1 C kg-1 =

per kilogram, 3.9 x 103 R C kg-1 Absorbed Gray (Gy) joules per rad (rad) 1 Gy = 100 rad dose kilogram, J kg-1 Dose Sievert (Sv) joules per rem (res) 1 Sv = 100 rem equivalent kilogram, J kg-1 Activity Becquerel per second, curie (Ci) 1 Bq =

(Bq) s1 2.7 x 10-11 C1

l esmC Pones 335 W S. NUC4E.m a EQut. ton T Commasaspose i .tromi tu.et4 sdwi.e #F IloC 888 W88 %# . 889 i

/ l s'E 7 BIBLIOGRAPHIC DATA SHEET NUEEG/CR-4286

• Ib3 SEE e%5TavCTIO%(One T=E mEvgnst 2 TITLE .%D 5V9 f t , Jtg.vtOL.%u Evaluatio of Radioactive Liquid Effluent Releases from the Ra ho Seco Nuclear Power Plant .jan . .o r co uno 07 - l j i mut-oam Dogsber 1985 i D. Cottrell, J. M. Loar, /

• o a " "'*o"' '5"' o I C. W. Miller, J. P. Witherspoo / l 1986

/ March

> .... o ..so o.a.~iz.1.o% %... .w ..t..o .oo. ss ., i, c , g ..o. c, a. wo.. v a so... a Oak Ridge National boratory " " * '"' " ""

Health and Safety Re arch Division P. O. Box I Oak Ridge,'IN 37831 A9468

. . ,,.m ,, c , ,,. ,,,,o,..,0.,

.o o~so .~oo.s.s,1 1.o~~....so..<,so.c Division of Pressurized Wa r Reactor Licens* g-B Technical Office of Nac1 ear Reactor Re 1ation . .. ..oo co s . . o , . ,

U.S. Nuclear Regulatory Commi ion Washington, DC 20555 12 $U, LE.1%T m v hoYt3 13 A557 #.CT #200 woras er '.naz A project has been carried out by Oak- Ridge National Laboratory (ORNL) to estimate the concentrations of dion lides in the environment that have resulted from the release of radioactiv9 materia s in the liquid waste effluents from the Rancho Seco (RSNPP and to estimate possible radiation doses NuclearPowerPpant concentrations. To carry out the to man resulting from carren environment objectives of this proj ec , two visits v e made to the RSNPP site by scientists from ORNL during November and December o 1984 to conduct an environmental sampling program around the site. Eleva d levels of some radionuclides were l found in the immediate e ironment of the plan This radioactive contamination occurs primarily alos streams receiving ef sent from the plant and in fields irrigated with water fy[ou these streams. The pro ary contaminants are 137C s and 134Cs with lesser atiounts of 60Co and 58Co. cific pathways of exposure and l

usage factors were n i precisely known for the dos assessment of current and

! potential use of ontaminated water and soil aroun the RSNPP. The ingestion of fish is the single most important pathway identified this analysis.

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