ML20210R060
| ML20210R060 | |
| Person / Time | |
|---|---|
| Site: | Rancho Seco |
| Issue date: | 02/24/1986 |
| From: | NRC |
| To: | |
| Shared Package | |
| ML20210R052 | List: |
| References | |
| TAC-64735, NUDOCS 8605160032 | |
| Download: ML20210R060 (44) | |
Text
7 4 , 4 STAFF ASSESSMENT OF ENVIRONMENTAL RADI0 ACTIVE CONTAMINATION IN THE VICINITY OF THE RANCHO SECO NUCLEAR POWER PLANT
CONTENTS I. Introduction . . . . . . . . I.1 1.A. Background . . . . . . . I.1 I.B. Purpose of Report . . . . . . I.2 I.C. Dose Guidelines . . . . . . . I.2 II. Rancho Seco Nuclear Power Plant . . . . . 11.1 II.A. The Plant . . . . . . . II.1 II.B. The Problem . . . . . . . II.2 II.C. The Licensee's Study . . . . . . II.3 II.D. Summary . . . . . . . . 11.8 III. The NRC Investigation . . . . . . . III.1 III.A. The Study . . . . . . . . III.1 III.B. The Results . . . . . . . III.3 III.C. Summary . . . . . . . . III.4 IV. Assessment of the Environmental Studies . . . . IV.1 IV.A. Evaluation of the Licensee's Whole Body Counts . . . . . . . IV.1
- IV.B. Evaluation of Accumulation of Cesium in the Environment . . . . . . IV.4 l
l IV.C. Dose Calculations and 40 CFR 190 . . . . IV.6 l V. Conclusions and Recommendations . . . . . V.1 l
V.A. Disposition of Contaminated Land . . . . V.1 l
V.B. Disposition of Contaminated Food . . . . V.1 I
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V.C. Conclusion . . . . . . . V.3 References . . . . . . . . . Ref.1 RANCHO SECO ii. 02/24/86
TABLES II.1 Summary of LLL Fish Sample Results: Mean Concentration of Cesium in Fish Flesh . . . . II.9 II.2 Summary of LLL Fish Sample Results: Mean Concentration of Cesium in Stomach Content . . . . . . II.9 11.3 Summary of LLL Sediment Sample Results:
Radionuclide Inventories in Sediments . . . . II.10 II.4 Summary of LLL Dietary Survey Report:
Selected Individual Consumption Rates . . . . II.11 II.5 Summary of LLL Terrestrial Food Sampling Report . . II.12 II.6 Summary of LLL Soil Sampling Data: Concentration of Radionuclides in Soil Samples . . . . . II.12 II.7 SMUD Calculated Maximum-Exposed Individual Dose Based on LLL Environmental Sample Concentrations . . 11.13 III.1 Summary of ORNL Fish Sample Results: Mean Concentration of Cesium in Fish Flesh . . . . III.5 III.2 Summary of ORNL Silt Sample Results . . . . III.5 III.3 Summary of ORNL Terrestrial Food Sampling Report . . III.6 III.4 Summary of ORNL Soil Sampling Data: Concentration of Radionuclides in Soil Samples . . . . . III.6 III.5 NRC Calculated Maximum-Exposed Individual Dose Based on ORNL Environmental Sample Concentrations . . . III.7 IV.1 Calculated Quantities of Radionuclides . . . . IV.9 RANCHO SECO iii. 02/24/86
- - =- .
FIGURES II.1 Comparison of Dose and Effluents with Applicable Standards and Guidelines . . . . II.14 III.1 ProjectedDosetoMaximum-ExposedIndividual . . . III.8 4
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STAFF ASSESSMENT OF ENVIRONMENTAL RADI0 ACTIVE CONTAMINATION IN THE VICINITY OF THE RANCHO SECO NUCLEAR POWER PLANT
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I. Introduction A. Background In May 1984 the Sacramento Municipal Utility District (SMUD) reported to NRC's Region V office that calculated maximum-exposed individual doses resulting from releases of radioactive liquid effluent from its Rancho Seco Nuclear Power Plant (RSNPP) exceeded the exposure standards of 40 CFR 190 (as enforced by the USNRC in 10 CFR 20.106(g)) for the period 1980 through the first quarter of 1984 (Ro84). The apparent violations went undetected until an examination of the environmental model in 1984 used to make the calculations revealed errors in input parameters used in the model. Because of the potential exposure to members of the general public, NRR contracted with Dak Ridge National
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Laboratory (ORNL)toconductanevaluationofthetypeandextentofthe contamination. To perform this evaluation ORNL scientists conducted an environmental sampling program around RSNPP. Sample items included fish, frogs, game birds, beef, soil, silt, vegetation, and water. Additionally, external radiation levels were measured to assist in determining the extent of ground contamination. Concurrently, SMUD contracted with Lawrence Livermore RANCHO SECO I.1 02/24/86
Laboratory (LLL) to perform an extensive and continuing radiological assessment of the effect of liquid discharges around RSNPP.
B. Purpose of Report This report has been prepared for the purposes of discussing and evaluating the extent of the radioactive contamination in the environment around the Rancho Seco Nuclear Power Plant (RSNPP), which is operated by the Sacramento Municipal Utility District (SMUD), and for providing guidance to Region V to determine if the requirements of 40 CFR 190 had been violated and if the dose standards provide therein were exceeded. To accomplish this purpose information submitted by the licensee and data developed by an NRR contractor have been evaluated and presented. The results of these measurements are presented in the Section II and III. As discussed in Sections IV and V, NRR staff has used these results to assess the environmental studies and to present conclusions regarding the extent of the problems and recommendations for minimizing potential harm to members of the public associated with the contamination.
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C. Dose Guidelines The principal dose requirement applicable to the Rancho Seco contamination l
is 40 CFR 190. This regulation specifies that nuclear power operations be conducted in such a manner as to provide reasonable assurance that the annual dose equivalent does not exceed 25 mrems to the whole body, 75 mrems to the thyroid, and 25 mrems to any other organ of any member of the public as a RANCHO SECO I.2 02/24/86
result of planned discharges of radioactive materials. This requirement is enforced by the NRC in 10 CFR 20.106(g).
Additionally, 10 CFR 50.34a requires that applications for a permit to construct a nuclear power plant filed after 2 January 1971 identify design objectives for keeping levels of radioactive materials in effluents to unrestricted areas as low as practicable. The guidelines for these design objectives, which are found in Appendix I to 10 CFR Part 50, require the applicant to provide assurance that the estimated annual dose to an individual from radioactive materials in liquid effluents be no greater than 3 mrem total body and 10 mrem to any organ. For these plants the Technical Specifications (TS) limit liquid discharges to the extent that these design objectives will be met. Because the application for a permit to construct RSNPP was filed on 20 November 1967,theAppendixIobjectivesdonotspecificallyapplytothis plant.
- t At the issuance of the operating license in 1975 the TS for RSNPP specified that the release of radioactive materials in liquid wastes, excluding tritium and dissolved gases, shall not exceed 20 Curies in any 12 consecutive month period. In addition, these initial RETS stated that the annual dose above background to the total body or any organ of an individual should not exceed 5 mrem in an unrestricted area. In the Summer of 1984 as part of a systematic program by NRR to incorporate design objectives required by 10 CFR 50.34a into TS for older plants not constructed in accordance with the design objectives, RSNPP implemented new TS approved by the NRC with these objectives.
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II. Rancho Seco Nuclear Power Plant A. The Plant As discussed in the Final Environmental Statement (NRC73) the liquid waste treatment system for RSNPP was designed'to treat the liquid wastes in a manner which would preclude the need for discharging radioactivity in plant liquid effluents under normal operating conditions. In particular, condensate 1 demineralizer regenerate liquids from resin regenerant, decontamination area
' drain, and steam generator drain liquids would not be released to the ,
environment.
1 1
However, in about 1980 leak's in the steam generator system began l
liberating increased quantities of radioactive waste in regenerant liquid from the spent resin beds. A substantial volume of radioactive liquid effluent l resulted from this action.
One method for handling liquid radwaste is to release acceptable amounts
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of radioactive materials to the environment via discharge into waterways. At RSNPP the waterway available is a stream called Clay Creek. Clay Creek was formerly a dry creek that carried overflow water from a reservoir during the wet season. However, commencing with operation of the plant, cooling tower blowdown has provided water to Clay Creek all year. -Stream flowrate is determined by the amount of water the plant chooses to release. The creek flows for approximately 3.5 km before joining the Hadselville Creek, the first RANCHO SECO II.1 02/24/86
waterbody to produce any dilution. The first 0.5 km of the creek lies within SMUD property. The remainder flows through grazing pasture and agricultural fields, land that has been generally available for cultivation or outdoor game sports such as fishing and hunting.
B. The Problem Beginning in 1981 large quantities of radioactive materials in liquid effluent were released to the environment as a result of normal operation of RSNPP. These quantities are displayed graphically in Figure II.1 and are compared to the TS liquid effluent limit. As shown in this figure, RSNPP did not violate the TS condition on release limits.
Figure 11.1 also depicts the calculated total body doses for the years 1980 through 1984. These doses were calculated by SMUD using a computer program called LADTAP II (Si80) and later confirmed by the NRC. This computer code was developed by the NRC and incorporates the liquid pathway dose models described in Regulatory Guide 1.109 (NRC77). These doses are compared to various dose standards and guidelines. From the calculations it has been determined that the principal contributing radionuclides are Cesium-134 and Cesium-137 and that the principal dose pathway is fish ingestion. The calculations indicate that both the TS radioactive discharge objective of 5 millirems and the EPA limit of 25 mrem have been exceeded during at least 3 of the last 4 years.
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An additional problem has arisen because of the long-lived nature of the principal contributing nuclides. Water from the stream has been routinely used by one of the farmers for flood irrigation purposes. It is thus expected that these nuclides will accumulate on the irrigated fields and will be incorporated into the crops grown on the fields. Accumulation of the radionuclides in sediment along the creek shoreline and in silt sediment in the creek will also occur. Accumulation of radionuclides in soil and silt is important for evaluating the long term effect of contamination of cultivated food, animal feed, and fish.
C. The Licensee's Study To investigate the extent of the problem and to determine if the standards of 40 CFR 190 had been exceeded, SMUD contracted Lawrence Livermore Laboratory (LLL) to perform an assessment of the problem including the analyses of samples taken from the environment. These samples included foods such as vertebrate and invertebrate fish, beef, and water fowl, as well as soil and sediment samples. LLL scientists also performed an aquatic and terrestrial dietary survey to determine the use of the contaminated land and creek. These analyses resulted in 4 reports each of which are discussed below.
The first of the the 4 environmental reports is entitled " Concentration of Radionuclides in Fresh Water Fish Downstream of Rancho Seco Nuclear Generating Plant (Nu84)." This report examines the effect of radioactive effluent concentrations on fish living in the creeks into which the effluent flows. Three principal species of fish, bluegill, bass, and catfish were RANCHO SECO II.3 02/24/86
chosen for the study because of their abundance and importance to sport fisherman. These fish were caught principally by rod and subjected to radiochemical analyses. In addition to studying the type and quantity of radioactive in each fish, the report attempts to deduce a relationship between concentration of radionuclide in the fish and the waterway distance from the plant.
Results of the LLL analyses indicate that Cesium-134 and Cesium-137 were the principal nuclides found in all species of fish with lesser amounts of Cobalt-60. The Cesium-137/ Cesium-134 ratio was relatively constant and ranged from 2 to 3 for all species of fish. Table II.1 summarizes the results of the LLL analyses.
The bluegill was considered to be the most appropriate indicator of maximum uptake of radionuclides mainly because of the territorial and nonmigratory nature of the fish. As a result, the report further investigated the feeding habits of this species of fish to @termine the relationship between radionuclide concentration in fish flesh and stream concentration.
Table II.2 presents data on the type and quantities of radionuclides released.
Additionally, Table II-2 presents limited data on radionuclide concentration in fish stomach content. LLL analyses found little correlation between water concentration and either fish flesh or stomach concentrations of radionuclides or temporal variations of these parameters. LLL has attributed this phenomenon in part to the diet of the analyzed fish. Laboratory results showed that bluegill stomach contents included ingested sediments for all periods except for the July catch. The fish caught during July were observed to be eating j RANCHO SECO II.4 02/24/86
insects and insect larvae near the surface of the creek. In support of this observation analysis of bluegill stomach contents indicated primarily the presence of insects for this time period. Little sediment or other benthic debris was found.
A second environmental report, entitled " Radionuclides in Sediments Collected Downstream from the Rancho Seco Nuclear Power Generating Station (Wo85)," examined the effect of radioactive effluent concentrations in plant effluent on the distribution of radionuclides in creek sediments. Creek sediments are potentially important because of their accumulation of radionuclides. Because of the bottom-feeding nature of several species of fish in the creek, most notably catfish, creek sediments are potentially concentrated sources of radionuclides available for food pathways to man.
Table II.3 displays some of the results of the LLL survey. As with fish, LLL found a good correlation between sediment concentration and stream distance from the plant. Examination of Table 11.3 reveals that the Cesium-137/ Cesium-134 ratio remains in the range of 2 to 3.
To attempt an estimate of the total quantity of each radionuclide in sediment, LLL scientists also performed a profile analysis of the sediment samples. The results of the initial analysis indicated that only about 20% of the released Cesium nuclides can be attributed to stream beds. LLL further concluded that the remaining 80% had been pumped onto field during irrigation.
Later work did not confirm this hypothesis. LLL ultimately concluded that much of the contamination had been transported downstream.
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A third report is entitled " Rancho Seco Liquid Effluent Pathway Aquatic and Terrestrial Dietary Survey Report (Ea84)." The purpose of the report was to identify all the potential exposure pathways to man resulting from releases of liquid radioactive effluent. Additionally, the report attempted to perform a land use census. LLL interviewed families who lived in the area to determine usagefactorsofstreamsandadjacentfieldandconsumptionratesofproducts from these streams and field. These data would be used to determine radiation dose to the maximum-exposed individual.
LLL determined the important pathways to man to be fish, frog, wild berry, wild duck, and wild pheasant consumption for internal exposure, and swimming, fishing, and irrigation pump maintenance for external exposure. Additional potential contributors to internal exposure were consumptions of crops, milk, and meat that had become contaminated through irrigated vegetation. No one family, however, was affected by all exposure pathways.
Upon review of this report Region V noted that information supplied to LLL by one of the interviewees conflicted with information obtained by Region V for the same individual. Because of this and other discrepancies, Region V informed SMUD that the land use survey was unacceptable.
SMUD in subsequent letter reports to the NRC updated their land use census (Ro85b and Ro85c). Table II.4 summarizes this information by individual and identifies user Z o as the maximum-exposed individual (Ro85c).
i The most recent dose assessment is based on this individual.
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4 The fourth and last report, entitled " Environmental Radiological Studies Downstream for Rancho Seco Nuclear Power Generating Station (No85)," summarizes f the data collected through the sampling program and evaluates the contamination problem at Rancho Seco. This information is obtained mainly from the 3 previously discussed reports. Table II.5 summarizes sampling data for terrestrial foods. In addition, the report also included the results of soil sampling that had been recently conducted so that a better understanding of the inventory of cesiums in the environment could be obtained. Table II.6 summarizes soil sampling data heretofore not available.
To assist in determining the actual intake of radionuclides SMUD subjected 2 families, including Z o,i to whole body counts (WBC). These WBC's were performed using a Helgeson whole body counting system. This system has a minimum detectable activity (MDA) of 6.3 nCi for Cesium-134 and 2.5 nCi for Cesium-137. No individual counted exhibited internal radionuclide activity, other than Potassium-40, greater than the MDA. For the purpose of determining an upper limit on the ingested quantity SMUD used the MDA of the equipment for their assessment.
Using the data from the WBCs, SMUD then calculated total body and liver doses for the exposed individuals. Table II.7 summarizes this information for the maximum-exposed individual. A discussion of the applicability of using WBCs for determining ingested radionuclides is presented in Section IV.
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D. Summary As a result of this investigation SMUD has calculated potential doses based on radionuclide concentrations in the environment. From the data produced by LLL SMUD calculated doses of 33 mrem to the adult total body, and 44 mrem to the adult liver. These doses result chiefly from the ingestion of 104 nCi of Cesium-134 and 224 nCi of Cesium-137 plus a smaller additional component from swimming and shoreline exposure. The calculated values clearly exceed the dose standards of 40 CFR 190.
To verify this calculation, real individuals identified by SMUD as living near the plant were given whole body counts. Whole body counts detected no activity other than naturally-occurring potassium above the detectable limits of the counting system. Based on this information SMUD has concluded that the maximum-exposed would have received no greater than 4.6 mrea to the adult whole body and 17 mrem to a child's liver. These resulting doses are less than the
-- dose standards of 40 CFR 190.
Finally, SMUD has performed a systematic check on the computer program used to calculate doses to assure that the program has been implemented properly and is functioning correctly. Agreement between SMUD results and rasults generated independently by the NRC using LADTAP II indicates that SMUD can satisfactorily execute the computer program.
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Table II.1 Summary of LLL Fish Sample Results Mean Measured Concentration of Cesium in Fish Flesh 1 Approx Distance Fish Type Mean Concentration (pCi/g)2 from Plant (km) Cesium-137 Cesium-134 O.5 Bluegill 11.0 5.2 Bass 7.2 3.1 4.6 Bluegill 4.4 2.0 Bass 2.8 1.2 12.6 Bluegill 0.5 0.2 Bass 0.5 0.2 19.5 Bluegill 0.1 0.1 Bass 0.1 0.1 1 Table 5 of No85 2 Background level not specified Table II.2 Summary of LLL Fish Sample Results Mean Measured Concentration of Cesium in Stomach Content 12 Collection Release Mean Concentration (pCi/g)3 Date (mci) Bluegill Bass Cs-137 Cs-134 Cs-137 Cs-134 Cs-137 Cs-134
_ 4-26-84 10.1 5.4 16.3 8.3 5-18-84 13.7 6.4 10.4 4.3 70.1 35.3 7-18-84 8.1 3.7 3.4 1. 8 37.0 10.2 8-14-84 22.9 11.7 7.3 3.1 1 Table 7 of No85 2 Samples were taken 0.5-0.6 km from the plant 3 Background level not specified 4 Releases positioned between 2 time periods occurred within the period between the 2 times RANCHO SECO II.9 02/24/86
Table II.3. Summary of LLL Sediment Sample Results Estimated Radionuclide Inventories in Sediments 12 Location Total Activity (mci)3 -
Cesium-137 Cesium-134 Retention basin 18.0 6.7 Clay Creek 24.4 11.0 Hadselville Creek 26.0 11.0 Irrigation Pond 25.0 9.7 (off Hadselville Creek)
Laguna Creek 6.3 2.5 Total F7 T03 Total Activity Released to Environment, 1981-1984 503 195 2 Table 4 of No85 2 Samples were taken during the period May-October 1984 3
Corrected for decay RANCHO SECO II.10 02/24/86
Table II.4. Summary of LLL Dietary Survey Report Selected Individual Consumption Rates 1 Pathway User (Adult)
Za Z3 27 Zo 2 i
Aquatic Foods (kg/yr) sunfish 3 0.5 2.3 5.7 11.3 bass 6.4 1.5 11.3 18.1 (16.3)4 catfish 4.5 6.8 2.3 -
frogs legs 9.1 3.4 -
4.5 (2.5)4 crayfish 0.9 - - -
Wildlife (kg/yr) duck 0.5 6.8 0.7 -
geese 1.3 - - -
pheasant 1.4 1.4 1.4 4.1 dove -
0.7 0.9 2.3 rabbit 1.4 1.4 -
7.7 Shoreline (hr/yr) fishing 480 240 75 1000 hunting 60 120 50 50 swimming - - -
1000 Other(kg/yr)
_ beef 55 66 - -
2Ro85b 2Ro85c 3The sunfish and bluegill are related species both of which appear to be relatively prevalent in the area. For comparison purposes these species are considered equivalent.
4 Parentheses indicate amount of consumed contaminated fish.
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Table 11.5. Summary of LLL Terrestrial Food Sampling Report 1 Sample MeanConcentration(pCi/g)
Cesium-137 Cesium-134 Berries nd2 nd Honey nd nd Milk 0.005 0.002 Beef 0.08 0.03 Duck 0.1 0.05 1 Appendix I of No85 2nd = not above detectable limits Table II.6. Summary of LLL Soil Sampling Data Concentration of Radionuclides in Soil Samples 1 LLL Sample ID Concentration (pCi/g)
Cesium-137 Cesium-134 RSP-1 1.87 0.45 RSP-2 3.89 1.22 RSP-3 1.46 0.25 RSP-4 1.14 0.09 RSP-5 0.63 0.08 RSP-6 0.49 0.04 RSP-7 0.63 0.06 RSP-8 1.00 0.16 RSP-9 0.96 0.11 RSP-10 0.66 0.03 1 Appendix VIII of No85 RANCHO SECO 11.12 02/24/86
Table 11.7. SMUD Calculated Maximum-Exposed Individual Dose Based on LLL Environmental Sample Concentrations 1 i
Pathway Mean Concentration Ingestion or Dose (mrem)3 Cs-137 Cs-134 Usage Rate 2 Total Body Liver Internal Aquatic Food Sunfish 10.5 pCi/g 5.0 pCi/g 11.3 kg/yr 15.3 21.3 Bass 4.8 2.1 16.3 9.7 13.6 i Frogs legs 10.5 5.0 2. 5 3.4 4.7 Wildlife Pheasant 0.05 pCi/g 0.01 pCi/g 4.1 kg/yr - -
Dove 0.05 0.01 2.3 - -
, Rabbit 0.05 0.01 7.7 - -
External Fishing 4.4 prem/hr 1000 hr/ 4.4 4.4 Swimming 0.1 prem/hr 1000 hr/yr yr 0.1 0.1 Total 32.9 44.1 1 Table 6 of Ro85c 2 Table II.4 of Ro85c 8 Three significant figures are used to provide consistency in calculations and do not imply the accuracy of these calculations.
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Figuro 11.1 COMPARISON OF DOSE AND EFFLUENTS WITH APPLICABLE STANDARDS AND GUIDELINES
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III. The NRC Investigatie 2 A. The Study In November 1984 NRR initiated a contract with Dak Ridge National Laboratory (ORNL) to conduct an evaluation of radioactive contamination around RSNPP. Theobjectivesoftheprojectweretodeterminethekindsand concentrations of radionuclides in the environment that had resulted from RSNPP liquid releases and to estimate possible radiation doses to man resulting from these releases.
To meet this objective, ORNL scientists visited RSNPP in November and December 1984 for the purpose of conducting an environmental sampling program in the area. Sample items included fish, frogs, game birds, beef, soil, silt,
, vegetation, and water. Additionally, external radiation levels were measured to assist in determining the extent of ground contamination.
During the course of the survey ORNL scientists measured external gamma radiation levels along the fields irrigated with creek water and along the banks of Clay Creek. Most measurements were performed using a gamma scintillation detector. However, to relate these measurements with actual environmental exposure rates, both pressurized ion chamber measurements and scintillation measurements were made at selected locations.
In addition to external gamma level measurements, soil and vegetation samples were t.aken. The external gamma levels were used to guide the sampling RANCHO SECO III.1 02/24/86
of these items. Soil samples were generally collected from an area 15 cm in diameter and 5 cm deep. To perform a profile of distribution of radionuclides in soil saraples, scientists at regular intervals pulled samples from a depth of 30 cm. Vegetation samples were also taken from areas having elevated external gamma levels. These samples were used to characterize the extent of contamination in the environment and to estimate the inventory of radionuclides outside of the creeks. Silt and water samples from the creeks were taken for a similar characterization.
Although external radiation dose is a component of the total radiation dose to man, it was determined from the beginning that ingestion of contaminated food would be the greatest contributor. To evaluate the potential dose from the ingestion pathway, samples of aquatic and terrestrial fauna were
! taken. Fish and frogs, where available, were taken from Clay, Hadselville, and Laguna Creeks as well as several ponds. Because of availability, the principal species of fish studied were the green sunfish, largemouth bass, and bullhead.
Since the concentration of radionuclides in fish is determined in part by fish size, only fish meeting a minimum size criteria were retained and analyzed.
Few frog samples were taken because of the scarcity of individuals during the
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i sampling period in November and December 1984.
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l In addition to fish, several game bird species were collected. Because of 1
the time of the year game bird samples were limited to the pheasant and the American coot. Finally, because cattle grazed on the contaminated fields, a
! cow was purchased for study. Appropriate cuts were taken from the slaughtered animal and subjected to laboratory analysis.
i RANCHO SECO III.2 02/24/86
The results of the ORNL assessment are detailed in a contractor report entitled, " Evaluation of Radioactive Liquid Effluent Releases from Rancho Seco Nuclear Power Plant (Mi85)."
B. The Results Elevated levels of radionuclides were found in water and silt samples immediately below the area where plant outfall forms Clay Creek. Levels decrease with distance downstream from the plant. The primary contaminants have been identified as Cesium-134, Cesium-137, and Cobalt-60. Cesium-137 was found in the greatest concentration. The Cesium-137 to Cesium-134 ratio was
- found to range from 2 to 3 and the Cesium-137 to Cobalt-60 ratio ranges from 10 to 50. Radionuclide concentrations in fish also declined with increasing distance. Concentrations in fish and frogs peaked at about 200 times background concentrations in Clay Creek. Other samples such as beef, game birds, and vegetation had significantly lower concentrations. The results of these analyses are summarized in Tables III.1, III.2, III.3, and III.4.
From these data it has been determined that consumption of fish and frogs is the greatest contributor to individual doses. Consumption of other foods as well as direct radiation from fields irrigated with contaminated water contributed only a fraction to the total estimated dose. Based on a land use census performed by SMUD the maximum-exposed adult is estimated by NRC to receive about 47 millirems annually as a result of radiocesium contamination.
The ingestion rates used for this calculation are presented in Table 111.5.
Whole body and liver doses to the maximum-exposed individual are also presented RANCHO SECO III.3 02/24/86
in Table III.5 and shown graphically in Figure 111.1. These values have been determined using an environmental dose model that is considered to be conservatively biased. Values of 0.0 in the figure indicate that these pathways do not exist for the maximum-exposed individual.
C. Summary The calculated results obtained by the NRC did not vary greatly from those of the licensee. Models similar to those found in R.G. 1.109 were used by both the NRC and the licensee. Only the actual measured radionuclide concentrations in fish differed. A comparison of Tables II.7 and III.5 indicates good agreement between ORNL and LLL environmental data for fish concentration.
However, the ORNL direct radiation component from fishing and swimming is more than twice the level as determined by LLL. The calculated values for whole body exposure are 33 mrem and 47 mrem for LLL and ORNL data, respectively.
Both values are greater than the dose standards of 40 CFR Part 190 and the TS objective.
RANCHO SECO III.4 02/24/86
Table III.1 Summary of ORNL Fish Sample Results Mean Measured Concentration of Cesium in Fish Flesh 1 Approx Distance Fish Type Mean Concentration (pCi/g) from Plant (km) Cesium-137 Cesium-134 0.5 Sunfish 10.03 4.78 Bass 8.96 4.07 Black bullhead 7.16 3.60 4.6 Sunfish 6.58 3.13 Black bullhead 9.21 4.41
- 9. 0 Sunfish 0.67 0.28 Black bullhead 0.39 0.46 15.5 Sunfish 0.13 0.07 Black bullhead 0.09 0.05 Background Sunfish 0.05 0.12 1 Table 5 of Mi85 Table 111.2. Summary of ORNL Silt Sample Results 1 Approx Distance Mean Concentration (pCi/g) from Plant (km) Cesium-137 Cesium-134 0.06 157 65
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0.6 86 35 0.7 115 45 3.2 97 42 4.0 58 24 10.0 4.2 1.6 Background 0.45 0.06 1 Table 3 of MiB5 RANCHO SECO III.5 02/24/86
Table III.3. Summary of ORNL Terrestrial Food Sampling Reportl Sample Mean Concentration (pCi/g)2 Cesium-137 Cesium-134 Frogs 0.06 <0.04 Game Birds American coot <0.07 0.27 Pheasant 0.21 0.13 Beef 0.02 0.005 Honey 0.006 nd3 1 Tables 4, A-8 and A-9 of Mi85 2 Background levels not specified 8nd = not above detectable limits Table III.4. Summary of ORNL Soil Sampling Data Concentration of Radionuclides in Soil Samples!
ORNL Field Number MeanConcentration(pCi/g)
Cesium-137 Cesium-134
_ 1 2.28 0.84 2 1.79 0.55 3 1.52 0.59
- 4 1.37 0.44 5 1.07 0.45 6 0.36 0.13 7 0.07 0.03 8 1.82 0.69 9 2.97 0.49 10 4.29 1.34 11 1.26 0.38 Background 0.33 <0.05 1 Table 2 of Mi85 RANCHO SECO III.6 02/24/S6
4 Table III.5. NRC Calculated Maximum-Exposed Individual Dose Based on ORNL Environmental Sample Concentrations Pathway Mean Concentration Ingestion or Dose (mrem)2 Cs-137 Cs-134 Usage Ratel Total Body Liver Internal Aquatic Food Sunfish 10.0 pCi/g 4.8 pCi/g 11.3 kg/yr 14.6 20.3 Bass 9.0 4.1 16.3 18.6 25.9 Frogs legs 10.03 4.83 2.5 3.2 4.5 Wildlife Pheasant 0.21 pCi/g 0.13 pCi/g 4.1 kg/yr 0.1 0.2 External L
Fishing 10.0 prem/hr 1000hr/yr 10.0 10.0 Swimming 0.2 prem/hr 1000 hr/yr 0.2 0.2
, Total 46.7 61.1 1From Ro85c 2 Three significant figures are used to provide consistency in calculations, and do imply the accuracy of these calculations.
8 Insufficient monitoring data; concentration for sunfish substituted.
4 d
RANCHO SECO III.7 02/24/86 i
f L .,_ . _ _ _ _ _ . _ _ - . . _ _ _ - - _ _ . _ __ _ . _ __ _ . _ ,. _ _ _ , _ _ _ _ _ _ _ . _ . - - . _ _ _ _ _ . - -
Figure Ill.1 PROJECTED DOSE TO MAXIMUM EXPOSED INDIVIDUAL (mrem /yr)
RANCHO SECO NUCLEAR FACILITY
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IV. Assessment of the Environmental Studies A. Evaluation of the Licensees's Whole Body Counts Whole body counts are generally considered to be an acceptable means for determining ingested quantities of radionuclides. Sensitive radiation detectors record radiation emitting from the body. Through careful calibration, spectral analyses, and sensitivity studies the quantity of individual radionuclides in the body can be determined.
When the quantity of each nuclide in the body has been determined, mathematical equations are used to estimate the quantity of a radionuclide at some earlier or later time. In the case of RSNPP, SMUD wanted to determine the quantities of Cesium-134 and Cesium-137 ingested by the maximum-exposed individual during the year immediately preceding the year of the WBC.
To perform this calculation the following equations have been used:
- 1. ) Fnr the case with no ingestion A(t) = Ag exp(-At) 2.) For the case with constant ingestion, I RANCHO SECO IV.1 02/24/86
A(t) =( I/A)*(1-exp(-At))
where A(t) = activity of nuclide present in the body at time t (days), in nanocuries Ag = Activity at t=0, in nanocuries A = removal coefficient for each nuclide, in days -1 I = Constant ingestion rate, in nanocuries per days For this application A is the sum of the biological decay constant, Ab ' I 8.3 x 10 4 day 1, and the physical decay constant, Ap , of 6.3 x 10 5 day 1 Since the actual consumption pattern of the maximum-exposed individual is not known, several ingestion scenarios have been considered. While no one scenario may be entirely appropriate, evaluation of the data from all scenarios will serve to bound the problem. Table IV.1 presents the results of these
~
scenarios including calculated quantities of Cesiums determined to be present in the body and the corresponding dose to a maximum exposed individual. As discussed in Section II.C., the MDAs for the Helgeson system have been used for these calculations since WBCs have shown no activity above the MDA. The MDA for Cesium-137 is 2.5 nCi and the MDA for Cesium-134 is 6.3 nCi.
RANCHO SECO IV.2 02/24/86
Of particular significance is whether the MDA of the Helgeson system is sensitive enough estimate the original quantity of ingested material. Based on the concentrations and the ingestion rate for the maximum-exposed individual as given in Table III.5, a total quantity of 285 nCi of Cesium-137 and 134 nCi of Cesium-134 has been ingested. Examination of Table IV.1 shows that for Cesium-137 and Cesium-134 the results of scenario 1 indicate that the MDA for the counting system is not sufficiently sensitive for calculating total nuclide ingestion back in time. Since the consumption of all fish on the first day of the year is not realistic, scenario 1 only provides an upper bound. On the other hand, for scenario 2 the results would indicate that the MDA for the counting system is sufficiently sensitive. Scenarios 3 and 4 are also evaluated. Scenario 4 provides an appropriate lower bound. Scenario 3 is similar to scenario 2, except that the fish consumption period is longer.
Scenario 2 is considered by the staff to be the most reasonable choice becauses it apportions consumption over an assumed fishing season. Scenario 3 was used
~
by SMUD as the appropriate scenario. The individual ingestion rates for water and terrestrial animals have not been questioned. Although the statistics for the measurements are not given, it appears that whole body counting with the Helgeson system does provide sufficient sensitivity necessary for this study to determine the quantity of Cesium present in the body.
B. Evaluation of Accumulation of Cesium in the Environment l
Radionuclidesinjectedintosurfaceswatermayremainsuspendedinthe water or settle to the bottom of the water body through sedimentation processes. Those nuclides remaining suspended will be carried by the water RANCHO SECO IV.3 02/24/86
generally into other water bodies. These suspended nuclides are considered in terms of their concentration in water. Water concentration of radionuclides is used by many mathematical models to determine the concentration of a nuclide in another chain of the the pathway. For example, in many models water concentration is used to determine fish flesh concentration, drinking water concentration, and irrigation water concentration.
On the other hand, many nuclides may settle to the bottom of a creek or river through sedimentation processes. For example, measurements of samples taken from the Clinch River near ORNL have shown that about 90% of the releases of Cesium-137 was absorbed into sediment within 10 miles of the release point (JI83). Other studies have shown that nuclide concentration in sediment tends to be greater than the water concentration above it. As a result of sedimentation process, radionuclides generally become available to benthic organisms, which provide food to bottom-feeding organisms (NRC78).
Additionally, at RSNPP because of the shallow nature of Clay Creek, sediment canbepumpedontoadjacentfieldsduringtheirrigationprocess. In this manner, irrigation provides another exposure pathway.
The accumulation of radionuclides, particularly radiocesiums, in sediment, aquatic biota, and irrigated fields may present a constant source of exposure.
In the case of RSNPP LLL found catfish with an unusually high concentration of Cesium-137 during a month in which no releases of Cesium had occurred. Indeed catfish concentration has continued to be elevated even though no releases of liquid radioactive effluent were occurring (Ro85d). Since catfish are RANCHO SECO IV.4 02/24/86
i
- typically a bottom-feeding fish, it may be concluded that catfish are ingesting additional quantities of Cesium-137 from its foraging habits in sediment.
Both LLL and ORNL attempted to determine the inventory of radiocesiums in the environment. LLL has determined that about 20% of the released radiocesiums are present in creek sediments. ORNL has estimated that about 22%
of the radiocesiums are present in fields and ponds near the creeks. From these data it appears that between 40% and 50% of the radiocesiums released during the period 1981-1984 have been accounted for. The remainder of the inventory has probably been carried downstream into other waterbodies and possibly onto fields and into sediment not included in this study.
C. Dose Calculations and 40 CFR 190 As presented in Section II the licensee has used LLL environmental data to
, estimate doses to the maximum-exposed individual. By using site-specific ingestion and usage rates for adult Z o, the licensee, based on the mean i
measured concentration of radiocesium in food (Table II.7), has calculated a whole body dose of 33 mrem and a liver dose of 44 mrem. s In a similar manner, the NRC using data from Table III.5 has calculated a whole body dose of 47 mrem and a liver dose of 62 mrem. )
The mathematical models normally used for environmental assessment have beencharacterizedasdeterministicmodels,thatis,sjnglevaluesforeachof 3
theparametersinthemodelareusedtoperformthecalcuiation. However, single values fail to consider the potential spatial and temporal variations RANCHO SECO IV.5 02/24/86
that may occur in these parameters. A publication by Hoffman, Gardner, and Eckerman investigates the variability in dose estimates from various food chain pathways, particularly as it relates to Regulatory Guide 1.109 environmental models(Ho82). Calculated doses are particularly sensitive to such factors as measured concentrations, usage and ingestion rates, and the dose factors used to convert activity ingested to dose. Thus uncertainti'es in these values should be considered in the interpretation of calculations based on observed data.
Uncertainty analyses attempt to consider errors in measurements, deviations in dose conversion factors among published sources, variations in consumption patterns, and so on. While no uncertainty analysis, which uses a statistical approach, has been attempted here, it is important to note the important parameters used for the calculations. The following equation, which is based on Regulatory Guide 1.109 models, has been used for these calculations:
D=Uf *(C cs-137
- DFcs-137 + Ccs-134
- DFcs-134 ) + Ufishing
- DR fishing (1) where D = whole body dose rate in mrem /yr l
l Ccs-134, Ccs-137 = measured concentrations of Cesium-134 and Cesium-137, 1
l respectively, in pCi/kg DFcs-134, DFcs-157 = dose conversion factors in mrem /pCi Uf = consumption rate of fish in kg/yr Ufishing = fishing time in hr/yr DRfishing = dose rate while fishing in mrem /hr l
l- RANCHO SECO IV.6 02/24/86 i
If we ignore that part of the equation related to direct exposure while fishing because of its relatively small contribution (cf. Tables II.7 and III.5), it is seen that changes in the fish ingestion rate, the radionuclide concentration in fish, and the dose factors can cause significant changes in dose. For example, both ORNL and LLL have errors in their low-level measurements of about 12% to 18%. The literature (cf Ho82) indicates potential variations of 100% or more among dose factors used to ccnvert ingested concentrations of radionuclides to dose. An'd if the annual ingestion rate of about 34 kg for individual Z o is i compared to Regulatory Guide 1.109 value of 21 kg and the Ho82 value of 14 kg for the maximum-exposed individual, it is evident that deviations of 50% to 100% from normal are possible. Indeed, in this last case, from Table II.4 individuals Z 3, Zs, and 27 seem to represent the usual situation.
As a result, calculations alone cannot conclusively determine dose. These I calculations must be considered with all available measurements. From the 1
foregoing analysis, when the results of the whole body count are considered,.it cannot be concluded that the whole body dose determined from environmental measurements exceeded the 25 mrem standard of 40 CFR 190.
h 1
RANCHO SECO IV.7 02/24/86
Table IV.1. Calculated Quantities of Radionuclides!
l Cesium-137 Quantity Dose (mrem)
(nCi) Total Body Liver Scenario 1 46.3 3.3 5.0 Scenario 2 14.2 1.0 1.5 Scenario 3 12.7 0.9 1.4 Scenario 4 5.1 0.4 0.6 Cesium-134 Quantity Dose (mrem)
(nCi) Total Body Liver Scenario 1 173.7 21.0 25.7 Scenario 2 44.6 5.4 6.6 Scenario 3 38.9 4.7 5.8 Scenario 4 14.3 1.7 2.1 Scenario 1: Entire consumption of Cesiums occurs on 1 January 1984 Scenario 2: Constant daily consumption from 1 March 1984 through 31 October 1984; no consumption thereafter Scenario 3: Constant daily consumption from 1 January 1984 through 31 December 1984; no consumption thereafter Scenario 4: Entire consumption occurs on 31 December 1984 1 Based on MDA of 2.5 nCi and 6.3 nCi for Cesium-137 and Cesium-134, at the time of measurement on 30 April 1985.
RANCHO SECO IV.8 02/24/86
V. Conclusions and Recommendations A. Disposition of Contnminated Land The land adjacent to Clay Creek is currently used for grazing and cultivating purposes. Since this land has been irrigated by Clay Creek water, Cesium-137 and Cesium-134 contamination is measurable in the fields. An evaluation of radiation exposure indicates that direct radiation exposure from ground shine will be the dominant dose component for long residence times on the fields. From Table III.5 a residence of 1000 hours0.0116 days <br />0.278 hours <br />0.00165 weeks <br />3.805e-4 months <br /> per year will result in a dose of 10 mrem from a high field along the creek. This number is based on the average of the measurements in the field. ORNL data indicates that the highest levels of contamination will occur near the irrigation outlet and decrease with distance from the outlet.
IflanddevelopmentweretooccurinfieldsadjacenttoClayCreek, residence time would necessarily increase. In this case it would be reasonable to assume a 100% residence time of 8760 hours0.101 days <br />2.433 hours <br />0.0145 weeks <br />0.00333 months <br /> per year. The radiation dose that would result from full-time exposure to the total accumulation of radionuclides in soil is about 90 mrem each year. In comparison the natural background radiation for this area is about 116 mrem per year (Figure 1). ,
l 1
B. Disposition of Contaminated Foods j i
A number of different types of foods are found in the area around RSNPP.
Among these foods are beef, milk, berries, game birds, and fish. All of these RANCHO SECO V.1 02/24/86
foods are consumed by the individuals who live in the area. Additionally, 2 of the foods have potentially commercial significance.
Cattle are allowed to graze on the pasture land irrigated with Clay Creek water. These cattle are raised principally as beef animals, but may also be used as milk animals. From Tables II.5 and III.3 the maximum measured concentrations in beef are 0.08 pCi/g of Cesium-137 and 0.03 pCi/g of Cesium-134. At these concentrations an adult who consumes a maximum of 110 kg per year of beef will receive a whole body dose of about 1 mrem. Similarly, at concentrations of 5 pCi/l for Cesium-137 and 2 pCi/l for Cesium-134 for milk, a teen who consumes 400 liters of milk per year will receive a whole body dose of less than 0.2 mrem per year. These consumptions rates are taken from Table E-5 of Regulatory Guide 1.109.
Fish in the Clay, Hadselville, and Laguna Creek are caught by sport fishermen and are a substantial part of some diets. As shown in Table III.5 an individual consuming fish at a rate of 30.1 kg/yr will receive a whole body dose of about 37 mrem each year from fish. At the consumption rate of 21 kg/yr as specified in Table E-5, of R.G. 1.109, the maximum-exposed individual will
~
receive a whole body dose of about 26 mrem each year. A final note is that even though SMUD has curtailed releases of liquid radwaste, concentrations in fish may remain at elevated levels because of the sediment concentration of radiocesiums.
RANCHO SEC0 V.2 02/24/86
Based on the consumption rates indicated in Table III.3 for other foods, such as berries and fowl, and the radiocesium concentrations in these foods, no individual will receive an additional whole body dose greater than 1 mrem each year.
C. Conclusion Based on this analysis it can be concluded that the radionuclide contamination in the area around RSNPP was the result of releases of liquid radioactive effluent from the plant. The primary contaminants are Cesium-134 and Cesium-137 with a smaller amount of Cobalt-60. Although the TS limit of 20 Curies for releases of liquid radwaste has never been exceeded, because of the unique situation at RSNPP in which Clay Creek is formed mostly by the plant itself, radionuclide concentrations in water were at a level to cause a maximum-exposed individual to receive a potential dose of about 50 mrem based on environmental measurements. This dose is based on measured radionuclide concentrations found in Table III.5, and Table 12 of Mi85, and ingestion rates from Table 111.5. If, however, the maximum-exposed individual consumed less fish than stated, or if other errors or uncertainties in parameters were considered, the calculated doses could be considerable different. !
l 1
In addition to these calculations, a whole body scan for the l maximum-exposed individual was performed for the purpose of determining the quantity of activity ingested. This count detected no radioactivity above the ;
minimum detectable activity of the system. The MDA is equal to about 7 mrem exposure to the whole body. Thus the whole body counts do not support the RANCHO SEC0 V.3 02/24/86
calculated dose. Thus it cannot be reasonably concluded that the 25 mrem dose standard was exceeded.
However, from a health and safety perspective, the environmental levels do not appear to be hazardous. Consumption of contaminated food, other than fish, will cause whole body doses of 1 mrem or less. Fish may cause an additional whole body dose of about 40 mrem maximum per year for the one individual, for whom fish is a major food staple. Other individuals are expected to receive no more than 60% of this dose based on the dietary survey conducted by SMUD.
Finally, because of the long physical half live of Cesium-137, radiation levels in contaminated fields will probably remain high over the years until weathering mechanisms and vegetation uptake remove them from the soil.
However, these levels will be no greater than the natural background radiation of about 120 mrem per year.
In summary, the data do not support a finding that an individual received a dose in excess of 25 mrem for 1984 as a result of releases of radioactive liquid effluent from RSNPP. It appears that no other federal standards or guides were potentially violated. Finally, the residual contamination may cause an additional, incremental dose of radiation to a person continuously living in the area of less than the natural background levels of radiation.
RANCHO SECO V.4 02/24/86
References Ea84 Eagle, R.J., Wong, K.M., Noshkin, V.E., 1984, " Rancho Seco Li Effluent Pathway Aquatic and Terrestrial Dietary Survey Report," quid Lawrence Livermore National Laboratory Report UCID-20267 prepared for Sacramento Municipal Utility District.
Ho Hoffman, F.O., Gardner, R.H., Eckerman, K.F., 1982, Variability in Dose Es imates Associated with the Food Chain Trans) ort and Ingestion of Selected Radionuclides, Oak Ridge National Laboratory, iUREG/CR-2612.
Mi85 Miller, C.W., Cottrell, W.D. Loar, J.M., Witherspoon, J.P., 1985, Evaluation of Radioactive Licuid Effluent Releases From the Rancho Seco Nuclear Power Plant," Dak Ricge National Laboratory, NUREG/CR-4286.
No84 Noshkin, V.E. , Eagle, R.J. , Dcwson, J.M. , Brunk, J.L. , Wong, K.M. ,1984,
" Concentrations of Radionuclides in Fresh Water Fish Downstream of Rancho Seco Nuclear Generating Plant," Lawrence Livermore National Laboratory Report UCID-20295 prepared for Sacramento Municipal Utility District.
No85 Noshkin, V.E. , Wong, K.M. , Eagle, R.J. , Dawson, J.W. , Brunk, J. L. ,
Jokela, T.A., 1985, " Environmental Radiolog"ical Studies Downstream from Rancho Seco Nuclear Power Generating Plant, Lawrence Livermore National Laboratory Report UCID-20367 prepared for Sacrament Municipal Utility District.
NRC73 U.S. Nuclear Regulatory Commission, 1973, Final Environmental Statement Related to the Operation of Rancho Seco Nuclear Generating
- Station Unit 1.
- NRC77 U.S. Nuclear Regulatory Commission, 1977, " Calculation of Annual Dose to Man from Routine Releases of Reactor Effluents for the Purpose of Evaluating Compliance with 10 CFR Part 50, Appendix I," Regulatory Guide 1.109.
NRC78 U.S. Nuclear Regulatory Commission, 1978, Liquid Pathway Generic Study, NUREG-0440 i
Ro84 Rodriguez, R.J., 1984, Letter dated 14 May 1984 with enclosure to J.B. l Martin, Region V, U.S. Nuclear Regulatory Commission.
Ro85a Rodriguez, R.J. ,1985, Letter dated 28 February 1985 with enclosure to J.B. Martin, Region V, U.S. Nuclear Regulatory Commission, Special Report 1 No. 85-01.
l Ro85b Rodriguez, R.J., 1985, Letter dated 15 March 1985 with attachment to J.B. Martin, Region V, U.S. Nuclear Regulatory Commission regarding Rancho Seco Liquid Effluent Pathway Usage Survey eport.
RANCHO SEC0 Ref.1 02/24/86
Ro85c Rodriguez, R.J., 1985, Letter dated 5 June 1985 with attachment to J.B.
Martin, Region V, U.S. Nuclear Regulatory Commission, Special Report No.85-05.
Ro85d Rodriguez, R.J., 1985, Letter dated 14 June 1985 with enclosure to J.B.
Martin, Region Rancho Seco Liqui V,d Effluent Environmental Study.U.S. Nuclear Regulatory Comm Sa8:, Sacramento Municipal Utility District, 1985," Radiation Exposure, Environmental Protection Effluent and Waste Disposal: January-December 1984 Annual Report," Rancho Seco Nuclear Generating Station Unit No.1.
Si80 Simpson, D.B., McGill, B.L., 1980, User's Manual for LADTAP II - A Computer Program for Calculating Radiation Exposure to Man from Routine Release of Nuclear Reactor Liquid Effluents," Dak Ridge National Laboratory, NURtG/CR-1276.
Wo85 Wong, K.M. , Eagle, R.J. , Dawson, J.M. , Brunk, J. L. , Noshkin, V. E. ,1985,
" Radionuclides in Sediments Collected Downstream from the Rancho Seco Nuclear Power Generating Plant," Lawrence Livermore National Laboratory Report UCID-20298 prepared for Sacramento Municipal Utility District.
l l
l RANCHO SEC0 Ref.2 02/24/86 l
l l
NUREG/CR-4286 l ORNL-6183 Evaluation of Radioactive Liquid Effluent Releases From the i Rancho Seco Nuclear Power Plant Prepared by C. W. Miller, W. D. Cottrell, J. M. Loar, J. P. Witherspoon O k Ridge National Laboratory uclear Regulatory Commission ff /) /1A O A A no l A f n />
- 7) L9 V '7 0 J u u l' ( VU ff
NOTICE This report was prepared as an account of work sponsored by an agency of the United States Government. Neither the United States Government nor 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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- 1. The NRC Public Document Room,1717 H Street, N.W.
Washmgton, DC 20555 i
- 2. The Superintendent of Documents, U.S. Government Printmg Olhce, Pmt Ollice Box 37082, Washington, DC 20013-7082
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Referenced documents available for inspection and copying for a fee from the NRC Public Docu ment Room include N RC correspondence and internal NRC memoranda; NRC Office of Inspection and Enfo cement bulletins, circulars, information notices, inspection and investigation notices; Licenser, Event Reports; vendor reports and correspondence; Commission papers; and applicant and licensee documents and correspondence.
The following documents in the NUREG series are available for purchase from the GPO Sales Program; formal NRC staff and contractor reports, NRC-sponsored conference proceedings, and NRC booklets and brochures. Also available are Regulatory Guides, NRC regulations in the Code of Federal Regulations, and Nuclear Regulatory Commission issuances.
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NUREG/CR-4286 ORNL-6183 Evaluation of Radioactive Liquid Effluent Releases From the t Rancho Seco Nuclear Power Plant i
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 1 Prepared for Division of Pressurized Water Reactor Licensing-B Office of Nuclear Reactor Regulation U.S. Nuclear Regulatory Commission W:shington, D.C. 20555 NRC FIN A9468
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CONTENTS Pane LIST OF FIGURES . ... .. . . . .. . . .. . . . . . ... . . . . . . . . . vii LIST OF TABLES . . . . . . . . . . .. . .. . . .. . . .. . . . . . . . .. ix ACKNOWLEDGMENTS . .. .. . .. . . . . . . . . . .. . . . . . . . . . . . . . xi ABSTRACT . . . . . . . . . . . . . .. . . . . .. . . .. . . . . . . . ... xiil EXECUTIVE sLAMARY , . . . . .. . . . . . . . . . . . . . . . . . . .. . . . xv
- 1. INTRODUCTION . . . .. . . . . . .. . . . . . . . ... . . . . . . . . . 1
- 2. SURVEY METHODS AND PROCEDURES . . . . . . . . . . . . . . . . . . . . . .. 5 2.1 MEASUREMENT OF EXTERNAL GAMMA RADIATION LEVELS . . . . . . . .. . . . 5 2.2 SOIL AND VEGETATION SANPLING . . . . . . . . . . . . . . . . . . . . . 5 2.3 SILT AND WATER SAMPLING . . .. . . . . .. . .. . . . . . . . . . . 7 2.4 FISH, FROGS, AND G AME BIRDS . . . . . . . . . . . . . . . . . . . . . 7 2.4.1 FISH . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8 2.4.2 FROGS . . . . . . . . . . . . . . . . . .. . . . . . . . . . . 11 2.4.3 GAME BIRDS . . . . . . . . . . . . . . . .. . . . .. . . . . 11
- 3. ENVIRONMENTAL SURVEY RESULTS . . . . . . . . . . . . .. . . . . . . . . . 13 3.1 TERRESTRIAL BACKGROUND MEASUREMENTS . . . . . . . . . . . . .. . . . 13 3.2 EXTERNAL GAMMA RADIATION LEVELS . . . . . . . . . . . . . .. . .. . 13 3.3 SOIL SAMPLING . . . . . . . . . . . . . . . . .. . . . . . . . . . . 14 3.4 VEGETATION SAMPLING . . . . . . . . . . . . . . .. . . . . . . . .. 14 3.5 SILT SAMPLING . . . . . . . . . . . . . . . . . . . . . . . . . . . . 22 3.6 WATER SAMPLING . . . . . . . . . . . . . . . . . . . . . . . . . . . 22 3.7 BEEF SAMPLING . . . . . . . . . . . . . . . . . .. . . . . . . . . . 24 3.8 HONEY 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 PATHWAYS OF INTERNAL EXPOSURE . . . . . . . . . . . . . . . . . . .. 37 4.1.1 INGESTION . . . . . . . . . . . . . . . . . . . . . . . . . . 38 4.1.2 INHALATION . . . . . .. . . . . . . . . . . . . . . . . . . . 44 4.2 PATHWAYS OF EXTERNAL EXPOSURE . . . . . . . . . . . . . . . . . . . . 45 4.3 ALTERNATE DOSE CONVERSION FACTORS . . . .. . . .. . . . . .. . .. 46
- 5. INVENTORY OF RADIONUCLIDES IN IRRIGATED FIELDS . . .. . . . . . . . .. . 47
- 6.
SUMMARY
OF RESULT 3 . . . . . . . . . . . . . . . . . . . . . . . . .. . . 51
- 7. REFERENCES . . . . . . . . . . . . . . . . . . . . . . . . . . . .. . . . 55 V
APPENDIX A. CONCENTRATION OF RADIONUCLIDES IN ENVIRONMENTAL SAMPLES . . . . . 57 APPENDII B. QUALITY CONTROL PROGDURES . . . . . . . . . . . . . . . . . . . 75 APPENDII C. RELEASE DATA . . . . . . . . . . . . . . . . . . . . . . . . . . . 93 APPENDIX D. ADDITIONAL PARTICIPANTS IN THIS PROJECT , . . . . . . . . . . . . 97 APPENDIX E. RADIATION UNITS USED IN THIS REPORT . . . . . . . . . . . . . . . 101 i
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LIST OF FIGURES Finure Pagg 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 Municips! 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 fields 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 irriaated fields at the confluence of a
Clay and Hadselville Creeks . . ... . . . . . . . . . . . . . . 19 8 Plat map showing Rarcho Seco Nuclear Power Plant and streams
) receiving liquid wastes from plant. Water and silt sampling locations are indicated on map . .. . . . . . . . . . . . . . . . 20 9 Typical irrigeted field showing division into sections for use in arriving at weighted average radionuclide concentration . . 48 A-1 California background sampling locations . . . . . . . . . . . . . 59 1
vil 4
LIST OF TABLES Table Pagt
- 1. Location and description of fish sampling sites in streams and ponds near the Rancho Seco Nuclear Power Plant . . . . . . . . . . 9
- 2. Average concentrations of cesium in soil, vegetation, and silt . . 21 I37 Cs and 134 Cs in silt from Clay, Hadselville,
- 3. Concentrations of and Laguna Creek . .. . . . . . . . . . . . . . . . . . . . . . . 23
- 4. Concentration of radionuclides in beef samples from Rancho Seco Nuclear Power Plant environs. . .. . . . . . . . . . . . . . 25
- 5. Mean concentration (pCi/g, wet wt.) of radionuclides in axial muscle of fish collected from streams downstream of The Rancho Seco Nuclear Power Plant, December 1984. . . . . . . . . . . . . . 27
- 6. Mean concentration (pCi/s, wet wt.) 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
- 12. Dose to a hypothetical individual from past liquid effluents from Rancho Seco . .. . . . . . . . . . . . . . . . . . . . . . . 52 A-1 Concentrations of radionuclides in California background soil samples . . . . . . . . . . . . . . . . . . . . . . . . . . . 60 A-2 Concentrations of radionuclides in soil samples . . . . . . . .. . 61 A-3 Concentrations of radionuclides in vegetation samples . . . . . . . 64 A-4 Concentrations of radionuclides in silt samples . . . . . . . . . . 66 A-5 Concentrations of radionuclides in water samples . . . . . . . . . 67
- l. A-6 Concentration of radionuclides in axial muscle of fish collected at various sites downstream of the Rancho Seco Nuclear Power Plant . . .. . . . . . . . . . . . . . . . . . . . . 68 l
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A-7 Concentration of radionuclides in axial muscle of fish collected from three small ponds near the Rancho Seco 4
Nuclear Power Plant . . . . . . . . . . . . . . . . . . . . . . . . 70 A-8 Concentration of radionuclides in axial muscle of frogs from two sites near the Rancho Seco Nuclear Power Plant . . . . . . 72 A-9 Concentration of radionuclides in axial muscle of game birds collected at several sites near the Rancho Seco Nuclear Power Plant . . . . . . . . . . . . . . . . . . . . . . . . 73 '
B-1 Comparison of gamma spectrometry results of soil sample analyses performed by two independent laboratories . . . . . . . . 78 i B-2 Comparison of radionuclide concentrations in duplicate tissue samples analyzed with NaI and GeLi detectors . . . . . . . . . . . 79 C-1 Liquid effluent releases (C1) from the Rancho Seco Nuclear Power Plant . . . . . . . . . . . . . . . . . . . . . . . . . . . . 95 i
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i ACENOWLEDGNENTS 1
l 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. Huckaba, S. White, S. R. Morris, and U. F. Strong for thei r untiring help in producing this report. We also thank B. G. Blaylock, K. F. Eckerman, C. T. Garten, D. C. Kocher, and A. S. Quist for their aid in reviewing earlier drafts of this manuscript.
l xi
l ABS'IRACT A project has been carried out by Oak Ridge Na tional 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 ef fluents from the Rancho Seco Nuclear Power Plant
. (RSNPP) and to estimate possible radiation doses to man resulting from current enviro nment al concentrations. To carry out the objectives of this proj ect, two visits were made to the RSNPP site by scientists from ORNL during November and December of 1984 to conduct an environmental sampling program around the site. Elevated levels of some radionuclides a
were found in the immediate environment of the plant. This radicactive contamination occurs primarily along streams receiving ef fluent from the plant and in fleids 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 amina 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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I EXECUTIVE
SUMMARY
Small leaks in the steam generation system at the Rancho Seco I
Nuclear Power Plant (RSNPP) , located 56 km (35 miles) southeast of )
Sacramento, California, have led to the release of aqueous radioactive Prior to the late summer of 1984, some amounts of l waste materials.
radioactivity thus generated were periodically released to the 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 rsdiation doses to man resulting from these releases.
To carry out the objectives of this proj ect, two site visits were made to the RSNPP by ORNL scientists during November and December of 1984 to conduct an envirotmental sampling program in the vicinity of the site. Elevated levels of some radionuclides were found in the immediate environment of the plant. This radioactive contamination occurs primarily along streams receiving effluent from the plant and in fields irrigated with water from these s t r e am s . 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 background levels in Laguna Creek approximately 19 km from the plant. The primary contaminants are 137Cs and 134Cs with lesser enounts 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 declined with increasing distance downstream of the RSNPP. Conce ntrations in green sunfish from Clay I
Creek at the plant boundary were 200 times background levels of the radionuclides sampled; concentraions 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 down st ream of the xv l
release point. The highest cesium concentrations occurred in largemouth bass collected from a sump 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 factors were not precisely known for the dose a s se s sment of current and potential use of contaminated water and soil around the RSNPP. The ingestion of fish is the dominant exposure pathway identified in this analysis.
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- 1. INTRODUCTION The Rancho Seco Nuclear Power Plant (RSNPP) is located
- l. approximately 56 km (35 miles) southeast of Sacramento, California, in Sacramento County. Operated by the Sacr ament o Municipal Utility l
District (SMUD), 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 steam-generator system have led to the creation of liquid radigagtive waste materiels. Th::c vsstes, as well as other waste waters generated by the RSNPP, are collected and treated in
' regenerate holdup tanks. Until late summer of 1984, the treated waters containing some amounts of radioactive fission and neutron activation products were periodically released to one or two on-si t e 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 137 Cs.
However, sa 11 amounts of 3H, 14 C, 60Co. and other radionuclides would be expected to be released during normal ope ra ti ons . As a result, selected environmental samples were screened for these radionuclides as well as for 54g ,, 238U , 90Sr, 238 p ,, 239p ,, 244 Am, a nd others (see Appendix C).
Substantial liquid releases of radionuclides to the environment are no longer occurring at the RSNPP. However, it is evident from Fig. 1 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 unposted areas in the RSNPP environs. Water taken from Clay Creek, J
Hadselville Creek, and other streams is used to irrigate pasture lands upon 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 possibic current radiation doses to man resulting f rem these releases. The purpose of this report is to document the results of this evaluation for use by NEC.
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 preliminary environmental samples 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 following:
- 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 ef fluent.
- 3. Concentration of radionuclides in fish, frogs, and birds found in or near the potentially contamin:ted waterways.
- 4. Concentration of radionuclides in soil and vegetation from fields irrigated with water from affected streams.
- 5. Concentration of radionuclides in beef from a cow that had i reportedly gra. zed on potentially contaminated pasture land, i
- 6. Concentration of radionuclides in honey.
Section 2 of this report discusses the methods and procedures used to obtain these environmental samples, summarizes end Sect. 3 the environmental concentrations that were measured. Section 4 presents the dose assessments that were performed for various potential pathways of L
4 exposure based on the results of the environmental measurement activity.
Estimates of the radionuclide inventory on irrigated fields are presented in Sect. 5, while Sect. 6 summarizes the results of the proj ect . The appendizes provide more detailed results of the 4
environmental sampling program.
It should be noted that current use of the land sampled in this study is for pasture only. No crops for hums: consumption are currently grown in these irrigated fields.
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- 2. SURVEY METHODS AND PROCEDURES 2.1 NEASUREMENT OF EXTERNAL GAMMA RADIATION LEVELS Gamma radiation levels were measured along the banks of Clay, Hadselville, and Laguna creeks and in fields identified as having been irrigated with wk.er from either Clay or Hadselville 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, external samma radiation levels were measured using both scintillation counters and pressurized ionization ch ambe r s . The relationship between these comparative measurements was used to convert scintillation counter 4 measurements to dose (exposure) rates.
For convenience in scanning, the irrigated land was divided into fields (irrigation units, Fig. 2). Each field was scanned using a gamma scintillation detector held approximately 5 cm from the ground surface.
Areas of elevated gamma radiation levels were noted, and the maximum 4
level observed was recorded for each area.
I 2.2 SOIL AND VEGETATION SAMPLING i
! Results of the radiation measurements made in the irrigated fields were used as a guide in selecting locations for soil and vegetation samplings. Generally, radiation levels were higher near irrigation pipe outlets and decreased with distance from the outlets in 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 gamma levels observed. Representative samples of both soil and vegetation f
l were collected from each area of each field. Samples were collected I: from an area 15 cm in diameter and 5 cm deep. At selected locations, to evaluate the depth of penetration of the contamination into the soil, I
samples were taken at 5-cm intervals from the surface to a depth of 30 cm. A total of 106 soil samples were collected from 80 sampling locations; however, because of resource limitations, only 57 sampler were subj ected to analyses.
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Schematic of the Rancho Seco Nuclear Power Plant environs showing the division of irrigated land into units (fields) for sampling purposes l
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Exploratory radiochemical analyses were performed on a limited number of- soil, silt, water, and vegetation samples. Based on the t
results of these analyses and on reported radionuclides discharged from the plant (Appendix C) together with their respective hazard indices, specific radionuclides were selected for inve st iga ti on. These radionuclides are given in Appendix 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). Aliquots of soil were counted on a Ge(Li) detector, and the spectra were analyzed by computer techniques.
Concentrations of 238U and 235U in selected samples were determined by e neutron-activation methods, and concentrations of alpha- and beta-emitting radionuclides were determined by radiochemical procedures (which are described in the ORNL master analytical chemistry manual).
Samples of vegetation were collected and placed in plastic bags and i
returned to ORNL for analyses. Vegetation samples were assayed as collected (wet) using techniques analogous to those used in assaying soil.
< 2.3 SILT AND WATER SAMPLING j
Silt (sediment) and water samples were collected from Clay, Hadselville, and Laguna creeks and from sumps and holding ponds used in
! the process of transferring water from Clay and Hadselville creeks to irrigate the pssture fields. Silt samples were dried, pulverized, and analyzed using the same procedures and methods as were used for soil samples. ,
Water samples were collected in 1 gal (3.S L) plastic containers and acidified with nitric acid (10 al, 70% HNO3/ gal) to minimize 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 60 Co in the flesh.
determine the concentrations of 137Cs. 134Cs, and t
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8 These. radionuclides were selected for analysis because they are routinely released from pressurized water reactors like that at the RSNPP and were found in a preliminary analysis of fish collected f rom the sump near Clay Creek in November. Because these radionuclides have relatively long hal f-live s (2 to 30 years), they can contribute a significant portion of the dose to man from fish consumption. No other gamma-ray emitters were found, either in the preliminary analysis of the November samples or in the analysis of selected s ample 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 (Appendix 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 from the small sump adj acent 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 electrofisher 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 st eam, depending upon fish densities at the site. Although the sump adj acent 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 bluegill, 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 sites (e.g. ,
Clay and Hadselville creeks), bluegill (Lecomis macrochirus) were not abundant. Consequently, the green sunfish (Lecomis cyanellus) was selected as a target species because (1) it was the dominant (most abundant) sunfish at most rites, and (2) it is large enough to be sought by anglers. Other target species included the largemouth bass (Microoterus salmoides), black bullhead (Ictalurus melas), and black crappie (Pomoxis niaromaculatus), which was found only in Laguna Creek
y Table 1. Location and description of fish sampling sites in streaus and ponds near the Rancho Seco Nuclear Power Plant Approximate distance Sampling Sampling downstream of Location #*** '
site- RSNPP (km)
Clay Creek At'SNUD 0.5 December'10, 12 property line t ,
4/
Hadselville Creek Just above bridge on 4.5 - December l12 ,
Clay Station Road c. * . r a X 4 Laguna Creek At Laguna Road 9.0 December 11
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, , s Laguna Creek 1.5 km above bridge , ,15.5 December 12 on McKenzie Road w .
Dry Creek 200 m below b' ridge December 12 (control) on Rtc. 104~
- Sump Just north of Clay Creek 0.5 November 14 at SMUD property line December 10, 12 s T /
Pond 1 0.5 km SW of SMUD 1.0 December 10 't '
0 property line
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6.0 December 11-adj acent to Hadselville ,
Creek ,
' Sampling site located approximately 14 km east of the, Rancho Seco Nuclear Power Pirat. -
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10 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 analyz a 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 sample was not obtained from Laguna Creek near McKenzie Road. High stream flows and turbid water made electrofishing difficult, and only a few small fish were collected.
Fish collected from each sampling site were placed in plastic begs, stored en dry ice, shipped within 1 to 3 d to ORNL, 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);
sexed, if possible; measured (total and standard lengths) to the nearest 0.1 cm; and, in most cases, weighed to the nearest 0.1 g. 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) individuals of the same species from different, but similar. sites (e.g., all stream sites, except Dry Creek, were combined).
A 6- to 15-g sample of axial muscle, excluding the skin, was removed from each fish. The sample was placed in a preweighed 25- by 150-mm glass tube, reweighed, and analyzed for 137C s, 134Cs, and 60Co with a Packard NaI(TI) detector assembly connected to a Canberra Series 35 multichannel analyzer. Samples collected on November 14, 1984, were analyzed on December 10, and the samples that were collected December 9-13, 1984, were analyzed January 14-17, 1985. Counting timior<
obtained from the U.S. Environmental Protection Agency (EPA)
Environmental Monitoring Systems Laboratory, Las Vegas, Nevada, and used to determine th e counting efficiency for each isotope. The detection limit for all analyses was 0.45 pCi per sample (1 dpm divided by 2.22 dpm/pCi).
11 2.4.2 Frons Cool temperatures prevented the collection of an adequate sample of frogs. Very few individuals were observed during daytime surveys along the stream banks and shorelines of the small ponds. Gigging was attempted af ter sunset in Laguna Creek but was unsuccessful. 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 g sample of axial muscle (similar in weight to that taken from fish) was removed from the hind legs of each frog; placed in a preweighed 25- by 150-mm glass tube; reweighed; and analyzed for 137C s, 134Cs, and 60 Co using the same procedures described for fish.
2.4.3 Game Birds Several game bird species were collected in December from fields and small 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 from the State of California, Department of Fish and G ame . A shotgun was used for all collections. On both the November and December sampling trips, waterfowl were not found in abcndance on the stre ams or small ponds near the RSNPP. Generally, only a few ducks, usually mallards, were observed at a given site. The low abundance and rather widespread distribution of waterfowl limited the co11setions to two coots.
Although recognized as a game bird by the State of California, which regulates the hunting of this species, the coot is probably not as popular with hunters as is the mallard or teal (several species). Two j 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 ig, and a 6- to 9g sample of axial muscle was taken from the breast.
Analytical procedures were the same as those described for fish.
I
- 3. ENVIRONMENTAL SURVEY RESUL'13 3.1 'IERRESTRIAL BACKGROUND MEASUREMENTS Background external gamma 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 RSNPP 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 pCi/g of 137Cs, effectively zero -
pCi/g of 134Cs, 0.73 pCi/g of 226Ra, 0.77 pCi/g of 232Th, and 8.3 pCi/g 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. Similarly, background levels have not been subtracted from radionuclide concentrations measured in environmental samples. However, doses from background locations were also calculated for comparison purposes.
3.2 EXTERNAL GAMMA RADIATION LEVELS External gamma radiation levels were measured with gamma scintillation counters (Nal). As discussed previously, comparison measurements were made with a pressurized ionization chamber (PIC) at a number of locations in the ficids 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 pR/h.
Gamma radiation dose rates in irrigated fields 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. Gamma dose rates measured over silt deposits along Clay Creek were as high as 38 pR/h at 1 m and ranged up to 85 pR/h at the surface. Dose rate measurements taken along the banks 13
14 of Hadselville Creek,15 m downstream from its confluence with Clay Creek, were 18 pR/h at Ia and about 60 pR/h at the exposed silt 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 semple locations were chosen to provide systematic unbiased sampling (i.e., sampling locations were systematically chosen within an area showing nearly uniform external gamma radiation levels). Locations of samples that were analyzed are shown in Figs. 3 through 8.
The primary radioactive contaminants found in soil samples were 137Cs and 134C s with lesser enounts of 60Co and 58Co. Concentrations of 226Ra, 238U , 232Th, and 40K were generally at background levels.
The
, maximum concentrations of 137Cs and 134 Cs were 59 pCi/g and 23 pCi/g, respectively. Consistent with gamma radi a ti on levels, the highest I
concentra ti ons 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 fleids. The weighted average concentrations of 137Cs and 134 Cs are listed by fields in Table 2. Complete analyses results are given in Appendix A Table A-2, 3.4 VEGETATION 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 soil samples. '
Vegetation sample locations are given in Figs. 3 through 7. As in soil, a
the radionuclides of primary interest are 137Cs and 134Cs.
Concentrations of 137Cs and 134Cs as high as 6500 pC1/kg and 2500 pCi/kg, respectively, were measured on a wet-weight basis in
! vege ta tion samples from irrigated fields. The concentrations of radionuclides in vegetation are distributed as in soil (i.e., higher near irrigation outlet pipes and decreasing with distance from the pipes in the- direction of water flow across the fields). Average concentrations of 137Cs and 134 Cs in vegetation samples are listed by l
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21 Table 2. Average concentrations of radioactive cesium in soil, vegetation, and silt Soil and silta Vegetationb Average radionuclide Average radionuclide concentration ~(pC1/g, dry wt) concentration (pC1/kg wet wt)
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 _. _ _ _
0 14 75 31 3510 1460 15c _ _ _ _
Sump 57 19 - -
Pond 1 0.70 0.12 - -
i Pond 2. 6.0 2.1 - -
aAverage radionuclide concentrations in soil are weighted averages; individual l concentration values are weighted according to the fraction of the total area represented by the sample bAverage radionuclide concentrations in vegetation are arithmetic averages, cFleids 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 sumps identified as having received water from Clay or Hadselville creeks. Samplins 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 in stretches of the stream bed where the stream flow is unimpeded and are subject to scouring during periods of high water flow.
, The maximum concentrations of 137Cs and 134Cs (157 pCi/g and i 65 pCi/g, respectively) were observed in Clay Creek near the RSNPP waste outf all and decreased downstream along Clay and Hadselville creeks, approaching background levels in Laguna Creek approximately 19 km i ,
downstream from the plant site. Concentrations of 137Cs and 134Cs in water silt along Clay, Hadselville, and Laguna creeks are given in Table 3. Complete analyses 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 Figs. 3, 7, and 8 for locations). Two water samples (RSW001 from the RSNPP outfall and RSWOO5
-from the mouth of Clay Creek) were subjected to radiochemical analyses.
The concentrations of all radionuclides analyzed were at or below the minimum detection r. mounts (NDA) 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 radionuclides found in these two samples and high flows observed in the creeks during the time of the i
survey, the rest of the water samples were not analyzed. Results of water sample analyses are given in Appendix A, Table A-5.
4 f 23
.1 Table 3. Concentrations of 137C s and 134Cs in silt samples from Clay, Hadselville, and Laguna Creeks.
~ 1' Sample location Concentration
- of radionuclide (pC1/3)
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 RSW5006 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 Lanuna 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 RSWS029 18 0.74 1 0.07 0.32 1 0.05 l RSWS002 19 0.26 1 0.06 0.15 1 0.03 r l l
aErrors associated with concentrations are 2 o (95% confidence l 1evel).
L
24 3.7 BEEF SAMPLING Beef cattle are raised on land along Clay and Hadselville creeks.
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 approximately ten years old, had spent most of 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 different parts of the animal, and one liver sample 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 gamma-ray spectrum contained only naturally occurring radionuclides with the exception of 137Cs. The 137Cs concentration was found to be 0.006 1 0.004 pCi/g.
The error given is the 2-a value for counting statistics alone.
3.9 FISH, FROGS, AND GAME BIRDS To estimate the dose to man from consumption of contaminated fish l and other vertebrates that are known to constitute at least a portion of the diet of some local residents, the concentration of radionuclides in f
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 l Appendix A, Tables A-6 to A-9.
r In the following discussion of these results, two maj or areas are emphasized: (1) evaluation of the adequacy of the data for purposes of dose assessment ard (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)a Sample. Type 137Cs 134 Cs RSCM-1 Back strap 0.01 0.005 RSCM-2 Shoulders 0.009 < 0.002 RSCM-3 Rib-eye 0.02 0.004 RSCM-4 Rond 0.009 < 0.004 RSCL-1 Liver 0.006 ( 0.003 "The counting errors associated with reported concentrations range from i 20% to 1120%.
l l
l l
26 I
discussion is based on the results of the 137Cs analyses because it contributes the maj ority 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 Elih Estimates of the radionuclide concentrations in fish focused on three spe cies : green sunfish (or bluegill at some sites), largemouth bass, and black bullhead that inhabit the streams and small ponds near the RSNPP (Tables 5 and 6, respectively). Based on preliminary information from local anglers and our own sampling by electroshocking, these species comprised the majority of the sport fishery in these small 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 cont amina t ed 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) individuals in the population. For example, Kolehmainen and Nelson (1969) found a direct linear relationship between total concentration of 137Cs and weight of bluegill over a range of weights from 1 to 70 g (Y = 9.26 + 0.391, r2 = 0.998);
concentrations of 137Cs (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 f rom 70.7 to 192.7 g) collected from a sump near the SMUD property line in Novembe r 1 984, (T A-7) indicated that fish exceeding 70 g did not have increased concentrations of 137Cs. The slope of the regression line (Y
= 9.93 - 0.03X, r2 = 0.41) was not significantly different from zero
[t-test, P (probability) >0.05 (Snedecor and Cochran 1967)].
Table 5. Nena concentration (pC1/3. wet vt.) of radionuclides is axial anscle of fish collected from streams downstream of the Rancho Seco Nuclear Power Fleet. December 1984.
(Less than values ignored la competion of mens; a = 3 for each species / site combination)
Species Green seafish Largemouth bass Black crappie Black balthead Sea lies 337 33, ,o 337 33, og 337 g, 33,Cs 137
- Co
- Co Cs 33*Cs Clay Creek 10.03 4.78 0.38 8.96 4.07 0.42 NC* 7.16 3.60 0.36 (1.73) (0.77) (0.28) (1.51) (0.78) (0.11) (0.72) (1.01) (0.38)
Bedselville 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)
Laguna Creek O.67 0.28 0.28 NA 1.58 0.78 0.15 0.40 0.39 0.46 (0.27) (0.33) (0.22) (0.37) (0.12) (0.17) (0.39) (0.12) (0.19) at Lassaa Ed Lagsas Creek 0.13 0.07 0.40 NC NC 0.09 (0.05 0.23 at McKenzie Rd (0.12) (0.02) (0.06) y
=4 0.12 0.44 NC NC NC Dry Creek 0.05 (control) (0.01) (0.13) (0.34)
- Nome collected.
bNambers in parentheses ladicate standard deviation.
'None analyzed; all ladividuals collected were small.
a = 1.
Table 6. . Mean concentration (pC1/3, wet wt.) of radionuclides la axial muscle of fish collected from small ponde near the Rancho Seco Nuclear Power Plant. November-December 1984.
(Less than walnes ignored in compation of mean; a = 3 for each species / site combination) species Green snafish Blaegill Larges ath bass anPl 8 Black ballhead 1#7 3 13 t Cs 13*Cs
- Co Cs 'Cs Co Cs "Cs
- Co 137 0s 13*Cs OU Co 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) u '
on
- None coIIected.
a = 8.
- Nambers in parentheses fadicate standard deviation.
1 i
l l r t
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29 I
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 and 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 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 from 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 sump 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 because (1) growth rates of bluegill in the two environment s may be 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 streams, such as Clay Creek, may have very few largemouth bass that exceed 30 cm (12 in.), local fishermen may keep bass that are less than 30 cm. Although only 50% of the largemouth bass collected in December 1984 exceeded 30 cm, all but one (92%) exceeded 25 cm; therefore, residents might be expected to consume fish of the smaller size. It is
30 Table 7. Percentage of the fish analyzed for radionuclides that exceeded the minimum quality length proposed by Gabelhouse (1984)
Species Sampling site Green Largemouth Black Black (All w M sunfish Bluegill bass crappie bullhead combined)
Nieiramqualitg 15(6) 15(6) 30(12) 20(8) 23(9) 1ersth, cm**
City Creek 100 0 33 44 H:ds31ville Creek 67c 100 83 Lag :a Creek at 67 33c 33 44 Laguna Rd.
Lag:xa Creek near 0 0 0 McKenzie Rd.
Dry Creek (control) 67c 67 Samp 88c 67c 67 79 P2nd 1 100 100 100 Pazd 2 0 33 Oc 11 Total (all sites 50 91 50 33 44 55 combined)
' Quality length is defined as the size of a fish most anglers like to catch
( And2rson 1980 as cited in Gabelhouse 1984) .
b Length in inches in parentheses.
- Excludes one fish that was within 1 cm of the minimum quality length criterion.
l 1
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 concentrations) 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 I
~
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 ect to the same bias because of the differences in fish weights betweet 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 g 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). i 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 i where one of the three individuals was small (Table A-6). Excluding i
32 these fish, all the others in Table A-6 exceeded the minimum quality-length criterion of 12 cm standard length and weighed more than 60 g.
Moreover, mean weights at each site exceeded 68 g (range: 69.4 g 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 were 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 downs tream of the source at the RSNPP (Table 5).
Although the three sampling stations below 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 RSWS004 and RSWS005) compared with concentrations in Clay Creek (sites RSWS006 and RSWS012) (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 from Hadselvile Creek have cesium levels that are not much lower than the levels in Clay Creek, about 4 km upstream near the SHUD property line.
Although concentrations of 137Cs in fish decline sharply 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 137 Cs in piscivorous speci,es ( fi sh-ea t e r s , such as largemouth bass and black crappie) exceeded that of nonpiscivorous
53 species in three of five possible comparisons; in Clay Creek and pond 1, concentrations of 137C s were higher in sunfish 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 137Cs 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 of 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 1370 s accumulation in bluegill and channel catfish can be greatly influenced by sediment composition, particularly the clay and organoclay complexes, which affects the availability of cesium for a s simil a tion. 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 bioaccumulation 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 lower Laguna Creek near McKenzie Road) with the lowest levels of cont am ina t ion (Table A-4).
Consequently, radionuclide concentrations in these frogs may be lower than if they were collected in more highly contaminated sites (Table A-8). The small sample size [one frog at each site, after
34 excluding a very small (37 g), unrepresentative individual from lower Laguna Creek] restricts the use of these data for dose assessment.
Because the frogs were collected from sites with the lowest levels of contamination, 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 i
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 individuals, 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 the RSNPP (Table A-9). Concentrations in all samples were relatively low and i
substantially lower than the concentrations in fish from Clay Creek.
Although local sportsmen probably prefer to hunt (and est) other species j 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 !
t i
food habits than many other waterfowl, preferring primarily aquatic l 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 factors for 137Cs in muscle tissue, for example, were estimated by Pendleton and Hanson (1958) to be 1800 and 2000, for the American coot and mallard, respectively. Moreover, the American coot is a year-round resident in the southern portion of its range [ Bent (1926)]. If this includes l
35 i
Sacramento County, their exposure to contamination would be greater than that of other species that are migrants in this region and breed in more northern latitudes. The winter and breeding ranges of the hserican coot, on the other hand, include California [ Bent (1926)].
i
s
- 4. RADIATION DOSE ASSESSMENT Radiation doses associated with the liquid radionuclide releases from the RSNPP were estimatea for a number of potential pathways of external and internal y exposure. Nessurements of radionuclide concentrations in en'virdament al media 'and edible food sources in the
. vicinity of Rancho Seco 'fadicated that only 60Co, 134C s 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 s ampl e s , several model calculations were made to indicate the magnitude of potential pathways of exposure associated with local contaminated land.
4.1 PATHWAYS OF INTERNAL EXPOSURE Individuals'living around Rancho Seco may be internally 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 contamiuted by irrigation ,
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 th- 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.
[ 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 doses are calculated for ingestion or inhalation pathways. The dose from the ingestion pathnay is given by [USNRC (1977)].
I D"3=(Cf) (Uf) (DFIg ),
I l
j where DI "8 = annual dose commitment to an indivivual due to the ingestion of radionuclide 1 (arem) 37 l 1
38 concentration of radionuclide i in ingested food Cf =
(pC1/kg) annual intake (usage) of food containing radionuclide Uf =
1 (kg) and DFI, = ingestion dose conversion factor for radionuclide 1 (aren/pCl) .
Slallarily, for the inhalation pathway [USNRC (1977)],
I D" =q (C") (R,) (DFAg ),
where Df"= annual dose commitment to an individual due to the inhalation of radionuclide 1 (arem)
C' = concentration of radionuclide i in air (pC1/m 3 );
R, = annual air intake for individuals (m )3and DFA g = inhalation dose conversion factor for radionuclide 1 (aren/pCl).
In this study it was assumed that R, = 8000 m3 [Rupp (1984)].
4.1.1 Innestion 4.1.1.1 Ehh Consumption of local fish represents the primary potential pathway of dose to individuals from RSNPP liquid effluents. Table 8 gives total-body and critical organ (liver) doses resulting from the ingestion 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 arem total-body dosc/kg ingested, respectively. Dose to liver, the critical organ, is about 1.4 times greater. Thus, consumption 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 arem/ year limit given in 40 CFR 190 [USEPA (1977)]. ,.
l l
39 Table 8. Radiation doses from ingestion of fish caught la the vicinity of Rancho Seco Dose (ares /kg ingested)
Location Number of -
samples Total M y Mver Clay Creek at 9 1.1 1.6 SNUD boundary Sump 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 McKenr.le Road Dry Creek at Rte. 104 3 0.02 0.03 (control) 1
40 Consumption of fish from other ponds in the area or from locations downstream from the Hadselville Creek sampling location appear to pose no problem because it is completely unlikely that an individual would have a yearly cons umpt i on of fish great enough (150 to 3500 kg) to exceed the 25-mrem limit.
Radionuclides contributing to the dose from consumption of fish are 137Cs (55.3%), 134Cs (44.5%) and 60Co (0.2%).
4.1.1.2 Frors and name birds Based on measured concentrations of radionuclides in frogs and game birds, consumption 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 mrem /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 soil sampled from field 1 (the most contaminated field), it was assumed that an individus1 eats leafy vegetables grown in this field. The resulting annual dose would be 3 x 10-5 mrem /kg ingested to the total body, 5 x 10-5 mrem /kg ingested to the liver.
This estimate is conservative because most of the soil samples taken in field 1 were taken in small areas where relatively high external exposure readings were given when the fleid was surveyed in a walk-over.
While this pathway of exposure is not currently available, the dose estimate se rve s to indicate that individual exposures from consumption of vegetables grown on this area would lead to less dose than would cons umpt i on of fish from the most contaminated aquatic sampling locations.
41
. Table 9. Radiation doses from ingestion of frogs and game birds caught in the vicluity of Rancho Seco Dose (alllirea/kg ingested) 3,,,,, Number of samples Total body Liver Frogs 3 0.01*(1.1)b 0.02*(1.6)b American coot 2 0.02 0.02 Pheasant 2 0.02 0.03
- Dose based on measured activity.
Dose based on assumption that frog flesh contains the same activity as fish flesh.
i i
, - - - , ,um, --,,-g ,e --
,- -- - , - - - , - - - - - - , - + n .~
42 4.1.1.4 Rtti Two estimates are given of the total-body dose to an individual eating beef from cows allowed to graze on fields 1 and 2 (Table 10).
Analysis of beef samples from a cow slaughtered December 27, 1984, indicated very low levels of 137Cs and 134Cs (1.08 x 10-2 and 3.6 x 10-3 pC1/g, respectively) . This cow was assumed to have grazed on fields 1 and 2 for several months. The resulting dose of 1.2 x 10-3 area / year (total body)/kg of beef lagested is indeed small. Estimated concentrations [USNRC, (1977)] for 137C s,134 Cs, and 60Co in beef based on average values of grass samples led to an estimated total-body dose of 4.6 x 10-2 mrem / year per kg ingested. This estimate is conservative, however, in that more grass samples were taken in small areas with the heaviest contamination in fleids 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 all owed to graze in contaminated fields around Rancho Seco wonid lead to doses greater than 1 arem/ year to an individual.
4.1.1.5 Milk Although allk cows are not raised on the contaminated fields 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 mrem /1 ingested (99.9% due to cesium radionuclides). Because of the relatively high cesium transfer factor from grass to allk, slik 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 mrem / year limit if it is assumed that all of the milk 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 ingested)
Source Total-body Liver Sampled cow 1.2 x 10-3 1.7 x 10-3 Model cow" 4.6 x 10-2 6.3 x 10-2
- Concentration of radionuclides in beef calculated from grass samples in fields 1 and 2.
l
44 4.1.1.6 Water Water from local streams carry ing 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 l
potential pathway of exposure. An upper limit of potential dose was estimated by assuming that an individual drinks water at the Rancho Seco outfall. The resulting total-body dose was 7.8 x 10-3 ares /L ingested with 94.4% from 3H, 5.4% from cesium, and 0.2% from other racionuclide s.
4.1.1.7 Honor Honey collected from a hive on a ranch bordering Clay and Hadselville Creeks contained small concentrations of 137Cs (0.006 pCi/g) and naturally occurring radionuclides. No 134 Cs was fousJ in these samples. Ingestion of this honey would result in a total-body dose of 4.3 x 10-4 mres/kg ingested for the 137Cs. This level of 137C s could result from weapons fallout [ United Nations Scientific Committee on the Effects 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 amount s 1
-of transuranic radionuclides (238Pu, 239Pu, 241Am, and 244Cm). The total activity was 1.1 x 10-2 pC1/g. It is estimated that 1 m2 og sogg would contain 17 9.2 pC1. Resuspension of these radionuclides into air by an amount of 10-9/m [Eckerman and Young (1980)] would lead to a lung l dose of 1.2 x 10-6 mrem for an individual breathing 8000 m3 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)'].
l
45 4.1.2.2 Other Radionuclides The resuspension into air of nontransuranic radionuclides in soil and subsequent inhalation by an individual represents one pathway of internal exposure around Rancho Seco. A dose estimate for this pathway was made by assuming average soil contamination levels in field 1 and a resuspension va'ue of 10-9/m for aged deposits. Total-body dose to an individual breathing these resuspended radionuclides was estimated to be 3.0 x 10-4 mrem / year. Because no individual would be exposed to this pathway for a full year, a dose of about 3.4 x 10-6 mrem for 100 h of exposure is more realistic. During cultivation, more deposited radioactivity is resuspended (10-5/m) so that an individual spending 100 h/ year cultivating fleid I would receive an estimated total-body dose of 3.4 x 10-2 mrem. These inhalation pathways would contribute little to maximum individual doses for persons utilizing contaminated fields around Rancho Seco.
Another potential inhalation pathway is associated with burning contaminated vegetation. Because rice is raised in the Rancho Seco area and the stubbic on rice fields is burned, dose from this pathway was estimated. It was conservatively assumed that field 1, with the highest levels of contamination, was used for cultivation of rice. It was further assumed that stubble mass (2.0 kg/m ) 2 contained the same level of contamination as grass sampled from field 1. Thus a total inventory of 156 pCi of 137C s, 59 pCi of 134C s, and 3 pCi of 60Co contained in the 3.5-ha field (8.61 acres) was assumed to be released in a fire of 30 min duration. Using an atmospheric dilution f actor of 3.6 x 10-3 s/m3 , an individual 100 m from the fire who inhaled contaminated air for the duration of the fire would receive a total-body dose of 1.3 x 10-2 mrem.
Thus, the inhalation pathway associated with burning of contaminated vegetation around Rancho Seco would seem to pose no significant dose problem.
1 4.2 PA'IIIVAYS OF EXTERNAL EXPOSURE l
Two pathways of external exposure are available for individuals around Rancho Seco. These are exposure from contaminated ground and exposure from swimming in contaminated water. Again, using average values of soil contamination in samples from field 1, an annual total-body dose of 73 mrem / year was estimated. Since no individual is exposed
46 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 CONVERSION FACTORS The internal dose conversion factors contained in USNRC (1977) were used in the calculations reported abose. However, more recent values 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 newer values are lower than the dose conversion factors given in USNRC (1977). For example, use of the values from Dunning et al. (1981) would lower the total-body doses due to ingestion of 134Cs by 44% and those due to ingestion of 137Cs by 31%. For inhalation, reductions in total-body I
dose would be 53% for 134C s 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 l
[USNRC (1977)] if the risk to persons living near the RSNPP is to be calculated.
i
- 5. INVBfIDRY 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 i- samp and ponds 1 and 2. Based on the concentrations of 137Cs and 134Cs found in the soil and silt sample s , an estimate of the amounts of these radionuclides remaining in the fleids and in the sump and ponds was made.
Each field was divided into areas based on the surface gamma <
radiation levels observed in each area. Soil sample results 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. The weighted average concentration for each 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 radionuclide contained in each field.
The relatisaship used in these determinations is as follows:
AK(C, - CB)
Q= ,
10 9 a where Q = quantity of radionuclides in field in sci, A = area of field in ft2, K = average weight of sample in g, Cs = weighted average concentration of radionuclide in pCi/g, CB = background concentration of radionuclide in pCi/g, and a = 0.1964 ft2, area of sample plus (6-in. diameter).
If substantial areas of a field 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 l
i l
48
- : a a : :-n : : : :
rIRRIGATION OUTLETS N o o o o o- -+o j SECTION A j
E x IRRIGATION FLOW SECTION B x
{
E a
I SECTION C a a 3
- L E
l SECTION D a
't 1 a
I R
a x x & a x x x x s x x :
, TYPICAL IRRIGATED FIELD l
Fig. 9. Typical irrigated field showing division into sections for use in arriving at weighted average radionuclide concentrations. ,
49 Table 11 lists the estimated quantities of 137Cs and 134Cs contained in each field, the sunp, and ponds 1 and 2. Analyses of depth 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. l Reported releases from RSNPP during the period 1981-1984 were 280.9 mci of 134Cs and 520.6 aCi of 137Cs (Table C-1). The quantity of 134Cs, when corrected for decay, becomes 174.1 aCl 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.
4 l
?
l
_ . . - , - - . - - . . . - - ~ --- - - - . - - - .
l 50 Table 11. Cesium inventory in fields, sump, and ponds 1 and 2 Quanity of radionuclide(mci)
Location 137 134 Cs Cr.
Field 1 7.40 3.17 Field 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 6.30 1.69 Field 12 Not sampled Field 13 Not sampled Field 14 23.50 9.52 Sump 4.81 1.61 Pond 1 0.09 0.02 Pond 2 0.87 0.32 Total 94.68 36.55 j
- 6.
SUMMARY
OF RESULTS The release of radioactive materials in the liquid waste effluants from the RSNPP has resulted in elevated concentrations of s ome radionuclides in the immediate environment of the plant. The 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 levcis approximately 19 km from the plant in Laguna Creek. The primary contaminants are 137Cs and 134C s with lesser amounts of 60Co and 58Co.
1 Radionuclide concentrations in fish also declined with increasing distance downstream of the RSNPP. Concentrations in green sunfish from Clay Creek ut the plant bounda ry were 2 00 times the background concentration of the radionuclides measured and decreased by 3S% in Hadselville Creek, approximately 4 km downstream. Although the same distance sepa ra ted the Hadselville Creek and upper Laguna Creek sites, concentrations in fish decreased by almost an order of magnitude. The highest cesium concentrations occurred in largemouth bass collected from a sump at the boundary of the RSNPP (mean values 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 tion in the irrigated fields and along streams receiving ef fluents from the plant. Gamma dose rates up to 38 pR/h at 1m 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 contoninated water and i
51 4
52 Table 12. Potential radiation doses to an individual from Rancho Seco liquid effluents" Dose (alllirem per unit exposure)
Source Toatal body Liver Internal Consumption of fish (per kg)b 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 f
Inhalation of vegetation fire 0.01 0.02 External Contaminated ground 8 -0.83 0.83 Swimming 8 0.002 0.002 "These doses cannot be added together without considering actual consumption or exposure data.
Average dose for three most contaminated areas.
c Assumes frog flesh is as contaminated as fish flesh, d
Dose based on measured sample.
- 100 h/ year cultivation.
Duration of fire is 30 min.
8 100 h/ year.
I
53 soil around Rancho Seco. However, it seems reasonable to assane that unless some 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 annuni doses associated with each year of release. Rather, this study gives estimates of dose associated with current environmental levels of contamination and potential pathways of exposure. Assuming no further liquid radionuclide releases from the RSNPP, future maximum individual i doses should be no greater than those estimated here because of radiological decay and additional dispersion of contamination in the environstnt.
i l
- 7. REFERENCES Anderson, R. O. 1980. " Proportional stock density (PSD) and relative weight (Wr): Interpretive indices for fish populations and c ommuni t ie s . " In: Proc.. Practical Fisheries Manamement: 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.
Bent, A. C. 1926. Life Histories of North American Marsh Birds.
Smithsonian Institution U.S. National Museum Bulletin 135. U.S.
Government Printing Office and Dover Publications, Inc. (1963), New York, p. 3 92.
Dunning, D. E. , Jr. , G. G. Killough, S. R. Bernard, J. C. Pleasant, and P. J. Walsh. 1981. Estimates of Internal Dose Eaulvalent to 22 Tarnet Ormans for Radionuclides Occurrina in Routine Releases from Nuclear Fuel-Cycle Facilities. Vol. III. NUREG/CR-0150 (ORNL/NUREG/TM-190/V3), Oak Ridge National Laboratory, Oak Ridge, Tennessee.
Eckerman, K. F. and M. W. Young. 1980. A Methodoloav for Calculatina Residual Radioactivity Levels Followina Decommissionina. NUREG-0707, U.S. Nuclear Regulatory Commission, Washington, D.C.
Eddy, S. 1969. The Freshwater Fishes. W. C. Brown Company, Dubuque, Iowa, p. 286.
Elwood, J. W. 1984. Mercury Contamination in Poolar 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 137Cs to Fishes from Ingested Clays." Verh. Internet. Verein. Limnol. 19:
2504-2509.
Gabelhouse, D. W., Jr. 1984. " A Length-categorization System to Assess Fish Stocks. " N. Am. J. Fish. Maname. 4:273-285.
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 137C12 Stable Cesium, and the Feedina Rates of Bluenill (Lenosis macrochirus Raf.) in White Oci Lake. ORNL-4445, Oak Ridge National Laboratory, Oak Ridge, Tennessee, p. 114.
l l
55
56 Miller, C. W. and F. O. Hoffman. 1983. " An Examination of the Environmental Half-time for Radionuclides Deposited on Vegetation."
Health Physics 45 (3):731-744.
Pendleton, R. C. and W. C. Hanson. 1958. " Absorption of Cesium-137 by Components of an Aquatic Community. " In: Proc.. Second Interational 6 Conf. on Peaceful Uses of Atomic Enerav. United Nations, Geneva, Switzerland, pp. 419-422. !
, v. ,
-p# P1 fle ger, W. L. 1975. The Fishes of Missouri. Missouri Department of ,
Conservation, Jefferson City, Missouri, p. 343. !
Rupp, E. M. 1984. " Adult Dietary Intake and Inhalation Rates. " In: i Nodels and Parameters for Environmental Radioloalcal Assessments, (Miller , C. W. ed.), DOE / TIC-11468, DOE Critical Review Series, Technical Information Center, U.S. Department of Energy, Oak Ridge, Tennessee, pp. 55-56.
Snedecor, G. W., and W. G. Cochran. 1967. Statistical Methods, Sixth Edition. Iowa State University Press, Ames, Iowa, p. 5 93.
U.S. Environmental Protection Agency. 1976. Radioloalcal Quality of lig Environment. EPA-520/1-76-010, Office of Radiation Programs, Washington, DC.
U.S. Environmental Protection Agency. 1977. 40 CFR Part 190, Environmental Radiation Protection Standards for Nuclear Power Operations." Fed. Remist. 42(9):2858-2861.
U.S. Nuclear Regulatory Commission. 1977. Calculation of Annual Doses is Man from Routine Releases of Reactor Effluents for the Purnose of Evaluatina Comn11ance 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. Ionizina Radiation: Sources and Biolonical Effects. United Nations, New York, N.Y.
Vanderploeg, H. A., D. C. Parzyck, W. H. Wilcox, J. R. Kercher, and S. V. Kaye. 1975. Bioaccamulation Factors for Radionuclides in l Freshwater Biota. ORNL-5002, Oak Ridge National Laboratory, Oak Ridge, Tenne ssee, p. 222.
Van Winkle, W., R. W. Counts, J. G. Dorsey, J. W. Elwood, V. W. Lowe, Jr., R. McE1haney, S. D. Schlotzhauer, F. G. Taylor, Jr., and R. R.
Turner. 1984. Mercury Contamination in East Fork Poolar Creek and Bear Creek. ORNL/TM-8894, Oak Ridge National Laboratory, Oak Ridge, Tennessee, p. 72.
APPENDIX A CONCENTEATIONS OF RADIONUCLIDES IN ENVIRONMENTAL SAMPLES k
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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 numbe rc 11'Cs 134Cs 60Co 58Co 54Mn 226Ra . 23 8U d -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 1.310.12 0.0720.08 (0.07 < 0. 0 8 <0.06 1.1 1 0.17 1.13 1.210.59 19 f 1.6 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 0.6110.08 0.0610.08 (0.05 (0.05 (0.04 1.1 1 0.22 1.28 1.5 f 0.5 9 2.1 f 0.69 4
CA8 0.33 f 0.09 (0.05 (0.06 (0.07 (0.05 0.7310.14 0.77 0.63 1 0.21 12 f 1.5 CA9 0.23 1 0.05 0.05 0.09 (0.03 (0.04 (0.03 0.55 1 0.11 0.49 0.4610.19 9.7 1 0.67 g CA10 0.26 f 0.99 (0.06 (0.06 (0.08 (0.05 0.55 f 0.09 0.46 0.4710.39 9.5 1 1.2 Call 0.07 1 0.05 0.03 1 0.03 (0.03 (0.04 (0.03 0.7810.13 0.68 0.74 1 0.17 13 f 0.76 CA12 0.89 0.15 (0.03 (0.04 (0.04 <0.03 0. 89 f 0.15 0.73 1.13 + 0.40 23 f 0.94 CA13 0.11 f 0.05 0.07 f 0.12 (0.03 <0.04 <0.03 1.16 1 0.13 0.56 0. 82 f 0.2 9 1420.82 CA14 0.2 9 + 0.0 9 (0.06 ' 0.06 (0.07 (0.05 0.65 1 0.04 0.53 0.7610.46 23 1 1.5 g(a CAIS (0.04 (0.03 (0.04 <0.05 (0.03 0.40 1 0.07 0.37 0.7810.37 35 f 1.0 aIndicated counting error is at the 95% confidence level (f 2o),
bConcentration values preceded by < are below the minimum detectable amounts (MDA).
cFor location see Fig. A-1.
dErrors associated with 23 8U concentrations are 1 5% (2a).
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Table A-2 (continaed)
Concentration s .b of radiosectide (pC1/s. dry weight)
Sample Depth numberc (ge,) 137Cs 134Cs 60c, SECo 54g, 2263 , 238U 232Th 40K Elsid_11 RSS072A 0-2 0.3830.05 0.06 3 0.03 (0.03 (0.03 (0.02 0.7920.08 -
0.71 3 0.23 1520.79 RSS073A 0-2 0.?820.07 (0.04 (0.05 (0.04 (0.04 0.90 2 0.11 -
0.78 2 0.32 1421.0 l
RSS075A 0-2 as 3 0.39 52 0.53 2.220.30 (0.10 0.3010.10 0.9830.16 -
0.83 + 0.20 1331.5 I
Elsid_11 RSS078A 0-3 (0.06 (0.04 (0.05 (0.05 (0.04 1.0220.2 -
0.84 2 0.43 8.620.93 RSS079A 0-4 (0.71 (0.04 <0.04 (0.04 (0.03 0.4810.08 -
0.35 2 0.13 4.7 2 0.83 eindicated consting error is at the 95% confidence level (3 2o).
bConcentration vetees preceded by < are below the aislaus detectable amoest (MDA).
CFor location see Figs. 2-6.
th te i
4 1
1 a
9 Is
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, _ . _ _ _ _ . _ _ _ _ _ . . _ _ _ _ _ . _ , _ _ _ _ . _ _ _ _ _ _ . _ _ _ _ _ _ _ _ _ . _ _ . _ _ _ __ . _ _ _ _. _ _ . __ _ m , m Table A-3 Concentrations of radiomectides la vegetation semples Concentratiosa .b of radionaalide (pCi/kg. wet weight)
Sample embe rs 137Cs 134Cs 6%, 58Co . .Seus 1 41Ce 144Ce 8'Sr 90s, 7, 3 40g 11eng, 131g U11d_1 R5V007 5940 f 270 2214 + 135 72.9 2 10.8 15.7 + 5.4 (11 (54 (270 (270 2970 + 270 1971 2 189 -
( 8.1 R5V008 3240 f 270 1107 3 81 51.338.1 RSV011 26 2 5.4 (11 (54 ( 270 (270 2376 3 189 2619 + 189 -
( 5. 4 2376 2 162 1053 3 81 40.5 3 2.7 - - -- - - - - - - -
RSV012 1782 2 108 675 f $4 8.130.81 - - - - - - - - - -
RSV015 192 1.9 (27 (27 - - - - - - - - - -
RSV019 - 70 + 5.4 (27 (27 - - - - - - - - - -
U sid 2 R5V020 2295 3 135 1188 + 81 95 3 5.4 - - - - - - - - - -
RSV024 146 2 B.1 594 + 54 24 3 2.43 - - - - - - - - - -
Usid.2 RSV027 20s 3 13.5 Its 3 s.1 (27 - - - - - - - - - -
RSv030 (27 (27 (27 - - - - - - - - - -
RSV031 (27 (27 (27 - - - - - - - - - -
Us14.1 RSV033 2079 2 135 756 + 54 40. 5 + 5.4
~
RSV034 251 f 16.2 135 _+ 3.1 (27 Usid.2 RSV03 : 165 2 11 7025.4 (27 - - - - - * - - - -
U sid f RSv051 (27 (27 (27 - - - - - - - - - -
Esv055 (27 (27 (27 - - - - - - - - - -
Usid_2 RSV042 1782 3 162 702 + 81 89 + 46 - - - - - - - - - -
R y047 15314 (24 (27 - - - - - - - - - -
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- RSV059 (27 (27 (27 - - - - - - - - - -
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g Tehte A-4. Cescentrattees of rednessetides is sitt semples Concentraliens .b of redlesocilde (pCA/ . dry seisnt)
S Sample numbe rs 137c. 134Cs 60Ce 38Ce 3dus 2263 , 238g 233Th 40g Cint Czssh RSW5001 157 3 1.7 6524.9 24 + 2.2 16 3 0.60 4.6 3 0.48 (1.0 1.22194 (1.3 7.0 + 3.0 8955006 13 5 + 1.62 45 3 3.2 13 3 1.7 3.4 + 0.46 1.4 2 0.37 (1.07 . 1.13194 (1.09 8.3 3 3.3 R55500 94 54 2 0.78 22 2 1.6 2.9 3 0.34 0.18 2 0.11 0.6 2 0.16 0.6920.4 -
0.9820.19 6.1321.43 E5W 501 De 33 + 0.52 1220.70 1.95 2 0.11 (0.10 0.33 3 0.11 1.0130.25 -
0.6920.39 6.01 2 1.3 Ess50114 57 21.2 23 2 1.8 1.9 2 0.32 1.04 3 0.36 0. 83 + 0. 27 1.02 2 0.26 -
0.92 3 0.20 7.832.8 3S55012 06 3 1.3 35 3 2.7 15 3 0.37 2.6 + 0.32 1.44 + 0.3 8 (0.99 -
(1.18 5.9 2 2.4 9262tL11112 CEtth 3555004 58 3 0.73 24 21.9 3.3 2 0.16 0.6220.12 0.4 8 + 0.15 (0.48 0.53 196 0. 06 2 0.44 13 + 1.6 l 2345005 97 2 1.38 42 + 2.4 10 + 0.3 5 1.420.38 1.0 g 0.31 ( 0. 83 1.24 + 15% 0.78 3 0.23 9.0 2 2.3 l 33s5034 0.45 3 0.09 0.06 3 0.06 (0.05 (0.05 (0.04 0.8920.07 -
- 0. 84 2 0.27 16 2 1.3 Lasten_Citth 3955002 0.26 2 0.06 0.15 2 0.03 (0.04 (0.04 (0.03 0.67 3 0.05 0.67 2 17% 0.66 2 0.18 s.e 2 0.71 )
E955003 2.5 3 0.08 0.9920.08 0.04 3 0.02 (0.02 0.02 3 0.03 0.5520.05 0. 81 3 1 st 0.6520.27 1220.66 RSe s021 4.2 2 0.11 1.44 + 0.2 0.08 3 0.03 (0.04 0.01 + 0.04 0.54 2 0.25 -
0.4 8 + 0.33 1120.81 3555029 0.74 2 0.07 0.3 2 + 0.0 5 (0.04 (0.04 (0.03 0.4430.13 -
0.4520.29 9.820.79 1sas gg RSW5013 16 + 0. 2 9 5.5 2 0.38 4.0 3 0.18 (0.08 0.22 + 0.08 0.53 3 0.05 -
0.4220.15 6.1 2 0.w3 ON RSB 5014 78 3 1.16 27 3 2.0 1220.84 0.43 + 0.23 0.74 3 0.26 0.6420.39 -
- 0. 89 + 0. 2 4 7.2 ; 1. 8 3555015 73 2 0.79 25 3 2.4 12 2 1.3 (0.18 0.74 3 0.21 (0.64 -
(0.54 7.4 2 1.8 tend _1 8955016 0.72 + 0.05 0.1920.02 0.05 3 0.01 (0.02 (0.02 0.57 3 0.09 -
(0.69 7.6 3 0.65 R35 5017 0.41 2 0.05 0.07 + 0.04 0.02 ; 0.02 (0.02 (0.02 0.57 + 0.11 -
0.7110.28 6.5 + 0. 5 9 RSs 5018 0.97 2 0.09 0.18 f 0.22 0.3 4 + 0.04 (0.06 (0.04 0.72 3 0.26 -
1.1 2 0.41 6.7 + 0.92 E95d_3 RSW5022 4.26 2 0.12 3.64 3 0.13 0.35 2 0.03 (0.07 (0.04 0.49 3 0.33 -
0.64 2 0.33 15 g 0.94 3955023 to 3 0.24 3.7 + 0.59 1.2 3 0.13 (0.09 0.13 3 0.08 (0.19 -
2.0 + 0.9 8 1231.4 RSW 5024 3.7 3 0.16 0.97 2 0.16 0.4220.03 (0.06 0.04 + 0.06 0.93 + 10 -
0.9130.29 1121.3 EsthAIP384 35W 5035 (0.02 0.02 2 0.02 (0.02 (0.02 (0.02 0.41 2 0.08 -
0.3 8 + 0.14 8 2 0.47 sledicsted coastles errer is at the 994 seaf fdence level (2 2e).
bConcestralien values preceded by ( sre below etsimum de tectable amesat s (MDA).
cFer locaties see Ft8s. 2. 3, 6. and 7.
40verflow from Clay Creek into Field 14
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Table A-6, Concentration of radionuclides in axial muscle of fish collected at various sites downstream of the Rancho Seco Nuclear Power Plant, December 1984 Total Standard Concentration Site Species Sex" length length Wel8ht (PC i/g, wet wt)
(cm) (cm) 137Cs 134Cs 60Co Cl ay Green M 17.4 14.8 101.1 b 12.02 5.66 0.48 Creek sunfish 16.8 b U 14.2 89.7 9.17 4.20 0.59 (Lecomis D F 15.2 12.8 66.3 8.89 4.48 (0.06 cyanellus)
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 (Microoterus 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 (Ictalurus U 17.0 14.5 60.5* 7.63 4.48 (0.07 melas)
Hadselville Green b M 18.5 16.1 129.2 10.48 4.60 0.41 Creek sunfish F 15.8 13.4 75.8 3.87 2.54 (0.06 M 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 Laguns Green M 14.9 12.5 71.3 0.81 0.66 (0.05 Creek at sunfish M 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 crapple M 19.5 15.4 115.2 1.28 0.71 <0.04 Pomoxis F 14.5 11.1 40.3 2.00 0.92 0.06 i laromaculatus) 1
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Table A-6 (continued)
Total Standard Concentration Site Species Sex" tength length eight (pC1/g, wet wt)
(cm) (ca) 137Cs 134Cs 60Co Black U 15.7 13.4 50.8 0.09 <0.05 0.23 bullhead d
Dry Creek Green M 16.3 13.9 85.4 (0.06 0.27 0.05 d
(control) sunfish M 15.2 12.4 62.1 d <0.05 0.05 0.60 M 12.3 60.6 0.05 0.05 0.66 "F = female; M = male; V = unknown; ND = not determined.
Estimated by: log 10W (fish weight in g) = -1.3953 + 2.9055 log 10L (standard length in cm), r2 = 1.00 and n = 26.
- Estimated by: Ic310W (fish weight in g) = -1.7577 + 3.0475 log 10L (standard length in cm), r2 = 0.99 and n = 20.
Estimated by: log 10W (fish weight in g) = -1.4208 + 2.9390 log 10L (standard length in cm), r2 = 1.00 and n = 8.
70 Table A-7. Concentration of radionuclides in axial muscle of fish collected from three small ponds near the )
Rancho Seco Nuclear Power Plant Total Standard Concentration Site Species Sex
- 1ength length Weight (pCi/g, wet wt)
(ca) (cm) 137Cs 134Cs 60Co b
Sump Bluegill F 15.0 12.5 70.7 11.10 5.77 (0.05 (Lenomis M 16.2 13.1 83.8 6.50 2.96 0.08 nacrochirus) U 16.2 13.2 89.2 5.76 3.09 (0.04 F 16.7 13.1 76.9 6.85 3.07 (0.05 b
U 18.4 14.6 148.6 5.72 2.55 (0.04 b
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 N 14.4 11.6 61.8* 3.94 1.51 0.59 Largemouth M 39.0 33.5 1,120.0 0 14.42 7.19 0.40 bass F 33.4 27.2 583.6 16.75 7.76 0.53 d
(Micronterus M 29.3 24.3 410.2 14.44 6.14 0.57 salmoides)
Black N 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)
P nd 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 Pend 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 (Lenosis U 9.6 7.8 18.9 0.81 <0.11 0.61 cyane11us) l i
71 Table A-7 (continued)
Concentration Total Standard eight (pCi/3, wet wt)
Site Species Sex
- 1ength length g)
(cm) (cm) 137Cs 134Cs 60Co Largemouth M 33.0 27.8 754.6 4.48 1.90 0.27 bass F 25.7 21.2 263.8 3.52 1.76 0.14 M 25.5 21.2 264.6 1.48 0.34 0.31 Black U 22.5 19.0 162.2 0.78 <0.06 0.55 bullhead U 18.6 15.8 92.9 0.71 0.06 0.58 l U 14.1 11.9 35.1 1.25 1.11 0.34 "F = female; M = male; U = unknown.
I Fish collected on November 14, 1984; all other fish were collected on December 10-12, 1984.
- Estimated by: log 10W (fish weight in g) = -1.4773 + 3.0704 log 10L (standard length in cm), r2 = 1.00 and n = 21.
Estimated by: log 10W (fish weight in g) = -1.7219 + 3.1285 log 10L (standard length in cm), r2 = 1.00 and n = 17.
' Estimated by: log 10W (fish weight in g) = -1.7577 + 3.0475 l log 10L (standard length in cm), r2 = 1.00 and a = 20.
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72 Table A-8. Concentration of radionuclides in axial muscle of frogs from two sites near the Rancho Seco Nuclear Power Plant, December 1984 Concentration Site Species a Weight (pCi/s, fresh wt)
(g) 137Cs 134Cs 60Co Pond 1 bullfrog 292.8 0.06 <0.04 0.25 (Rana catesbeiana)
Laguna Creek ND 98.7 <0.06 0.11 0.27 near McKenzie ND 37.3 0.23 (0.08 0.31 Road "ND = not determined.
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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 3 ,,g,, 3,,a Weight Collection (pCi/g, wet wt)
(g) site 137Cs 134Cs 60Co American ND 539 Sump (0.08 0.08 1.21 coot (Fulica americana)
American ND 588 Pond 1 (0.07 0.27 0.14 coot Wil son ' s ND 1017 Clay Creek (0.07 0.13 0.33 snipe near SMUD (Canella boundary delicata)
American ND 630 Clay Creek 0.95 0.42 0.42 b
bitttern west of Rte 104 (Botaurus lentiainosus) l Pheasant M 1010 Field just north 0.31 (0.07 0.68 (Phasianus of Clay Creek and colchicus) west of Rte 104 Pheasant M 967 Field just south 0.21 (0.06 0.21 of Clay Creek and east of Rte 104 "M = male; ND = not determined.
Not a game bird; species was collected because its diet, although varied, consists of small fish (Bent 1926).
1 APPENDIX B QUALITY CONTROL PROCEDURES '
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d 77 The radiological survey and analyses of environmental samples from the Rancho Seco Nuclear Power Plant environs was carried out within the general guidelines of Oak Ridge National Laboratory Quality Assurance Procedures.
The radiochemical analyses of environmental samples performed by the Analytical Chemistry Division were carried out within the controls provided by the division's Quality Assurance Program (copy attached). l In accordance with this program, the analytical laboratories within 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 Analytical 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 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 instrument is checked in the field daily for proper operation using uranium check sources.
High resolution gamma spectrometry instruments (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 independent counting facilities.
For the aquatic sampling program, the Environmental Science s Division used a NaI(TI) gamma 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 137C s, 134C s, and 60Co and scanned for other gamma r r-emmi8=~ radionuclides by the Analytical Chemistry Division using . : f,1 -t sor. Table B-2 gives the results of these two indepen , co ,ntration measurements.
u_ . _ __. - _ _. _ _ _ _ _ _ ._-- - . _ .-- ___ _ _ _
Tabl e B-1. Comparison of ganza spectrometry results of soil sample analyses performed by two independent laboratories Concentration of radionuclide (pci/s. dry weight)
WCs INCs 60Co 58Co 54Na Sample number RASAa ACb RASA* ACb RASAS ACb RASAs ACb RASA* ACb RSS001 7.7 + 0.20 7.7 1.7 2 0.42 1.7 4.9 3 0.25 4.6 (0.0 9c -
0.33 3 0.09 0.37 RS$002d 33 3 0.84 34 13 2 0.91 12 6.0 f 0.03 5.7 1.4 1 0.32 0.37 0.64 f 0.27 0.63 RSS006 12 2 0.41 13 4.930.65 4.5 1.4 2 0.05 1.4 (16c 0.07 0.2220.12 0.24 RSS007 22 f 0.36 22 7.3 f 0.95 6.7 2.7 3 0.21 2.5 (15c -
0.4910.11 0.50 F.SW50018 155 f 1.7 140 6534.9 57 2912.2 26 16 f 0.60 14 4.610.48 3.8 RSWS002 0.26 2 0.06 0.26 0.1520.03 0.13 (0.04c -
(0.04c - <o,03c _
RSWS006f 115 f 1.6 100 45 2 3.2 40 13 1 1.6 11 3.4 1 0.46 3.2 1.4 1 0.37 1.4 ;j sAnalyses performed in the Radiological Survey Activities (RASA) Group counting f acility at Oak Ridge National Laboratory. Errors associated with these concentrations are 2e (95% confidence level).
bAnalyses performed by the Analytical Chemistry Division of Oak Ridge National Laboratory. The overall uncertainty in the concentrations of major constituents is 110% (2a); the uncertainty of minor constituents is of the order of +
25%.
cConcentrations arc less than the minimum detectable amount (KDA),
d110 mag - 4. 8 pCi/s.
e110 mag - 1.3 pC1/3
, f110 mag - 0.66 pCi/g.
79 Table B-2. Comparison of radionuclide concentrations in duplicate tissue samples analyzed by the Environmental Sciences Division, and in parentheses with 95% confidence interval, the Analytical Chemistry Division Sample Sample Sample Concentration (pCi/g)
Numbe r Description Location 18'Cs 184Cs **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 Largemouth Pond 1 0.24 0.06 (0.03 bass (0.32) (<0.08) (<0.11) 6 Largemouth 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)
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QUALITY J"y;L ASSURANCE PROGRAM i
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i ANALYTICAL !
CHEMISTRY :
DIYlSION t
'*****'*'m- -
1 81 QUALITY ASSURANCE PROCEDURE l OAK RIDGE N ATIONAL LABORATORY ~ '""' ' Q A- AC D- 1 8-1-83 QUALITY ASSURANCE PROGRAM -
3,3 CJPE N%t Cf 5 IS%ul D A TI C TITLE:
ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM POLICY STATEMENT l
I In accordance with the Quality Assurance Program goals established by the Director of the Oak Ridge National Laboratory (ORNL), it is the policy of the Analytical Chemistry Division (ACD) to establish, main-tain, and enforce an ef fective quality assurance program. This effort is designed to meet the requi rements 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.
I 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 members are responsible for applying the app ropriate quality assu rance 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.
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OAK RIDGE NATIONAL LABORATORY O*E R A TI D BV UNION CARBIDE CORPORATION huCit AR Divl$i0i Approved By: -
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82 QUALITY ASSURANCE PROCEDURE OAK RIDGE N ATIONAL LABORATORY OA-ACD-1 8-1-83 QUALITY ASSURANCE PROGRAM -
1 cr 5 r
i su,c ostees ,ssut c.uo TITLE:
ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM
- 1. Mission of the Division The Analytical Chemis try Division (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, an't 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/ Development 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 th reaten the p rogram. Controls fall into three areas: (1) peer review in either formal or informal meetings, (2) mandated quality assurance 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 l
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:
l l (1) quality control samples prepared by ACD to be simila r to i 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.
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OAK RIDGE N ATIONAL LABORATORY ,
onenarro av l UNION CARBIDE CORPOR Ail 0N NUCLl80 DIV$CN Approved By: ____O D b uc ...s e
83 UAW ASSMCE NOCEME OAK RIDGE N ATIONAL LABORATORY e.ww e >.
QUALITY ASSURANCE PROGRAM -
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TITLE: ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM i 1
- 3. Responsibilities
- 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 Informs 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 failure and audit reports.
3.2.5 Reviews and approves division QA assessments and QA plans.
3.2.6 Performs internal audits and assists others in perform-ing audits.
3.2.7 Interprets quality assurance procedures for the division.
3.2.8 Produces an annual report of QA actions.
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84 OUALITY ASSURANCE PROCEDURE OAK RIDGE NATIONAL LABORATORY .ouem o.
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OA-ACD-1 QUALITY ASSURANCE PROGRAM --
3 ,, 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 and approves section QA plans.
3.3.3 Reviews Group / Task Leader actions to ensure that these responsibilities are discharged. j 3.4 Group / Task Leader 3.4.1 Plans the R/D or support program for the group assisted by the scientists involved. i 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 rogram.
3.4.5 Initiates a Quality Investigation Report (QIR) 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 employees of their roles in providing assurance of quality. The QAC will make periodic reports to ACD supervisory personnel on cur-rent QA procedures and directions. The division will comply with guidelines described in QA-L-1-102 and participate in activities such as QA week and video tape presentations.
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- #8 OAK RIDGE N ATIONAL LABORATORY ,% u u t oo.
QUALITY ASSURANCE PROGRAM 4 er 5 TITLE: 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 identify and evaluate the risk of potential significant quality problems (failure modes), and for each quality problem with an acceptable risk provide a rationale for the determination. For each ootential 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 programs 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 manuals shall be observed.
5.3.2 UCCND Standard Practice Procedure D-5-5 and ORNL QA p rocedure 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 periodically and appropriate j 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.
5.3.4 Resuits of research shall be published in ORNL docu- l ments, and in scientific journals, and presented at scientific meetings when appropriate.
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OAK RIDGE NATIONAL LABORATORY OA-ACD-1 QUALITY ASSURANCE PROGRAM -
5 e 5 TITLE: ANALYTICAL CHEMISTRY DIVISION QUALITY ASSURANCE PROGRAM 5.3.5 Any significant changes in the program or acti vity shall be discussed with the QAC to determine whether additional quality assurance procedures should be implemented.
5.3.6 All significant quality problems shall be investigated, 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, nonconforming items and others.
5.3.7 The retention and disposition of quality related i records shall follow the procedures described in QA-L-16-100.
1 5.3.8 Purchase of standard and special itens shall be accomplished in a manner to ensure adequate quality.
QA-L-9-100 (Rev. 2) describes these procedures and 1 references appropriate QA procedures for procurement ,
inspection, quality problems and others.
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OAK RIDGE l NATIONAL LABORATORY Analytical Chemistry
- - ~ ~ ~ -
Division l
l General and Environmental Analysis Section Quarterly Quality Control Report October-December 1984 1
OPERATED BY MARTIN MARIETTA ENERGY SYSTEMS,INC. ,I FOR THE UNITED STATES }
DEPARTMENT OF ENERGY
88 INTRA-LABORATORY CORRESPONDENCE OAK RIDGE NATIONAL LABOR AToRY 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 L AE :4500 B NUM LIMIT NUM.
OF OF 2si CA LC OUT BIAS 1ET!!OD: DET ER :C COD E TESTS ERROR FOUND 'T' % BIAS CNTRL SIGNIF 1
!!!EM SEP:S R-90 :RSRYS 11 +15.00 + 18. 0 0 5 -0.2180 -0.62 1 NO 2-SPEC: Co-60 : R CC5 : 14 +8.00 +3.176 + 2.152 8 + 0. 9 2 0 NO i-SP EC: CS- 137 : R CC 5: 12 +6.00 +1.407 + 8. 718 3 +1.80 0 YES LIQ SCINT:H-3: RTR 18: 3 +10.00 +0.036 + 2 4 7. 4 35 8 +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 4t quarter 1984 was 98%.
cc: W. R. Laing D. A. Lee R. K. Owenby L. M. Roseberry J. R. Stokely (2)
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PLO! 88 8 5.15.<.3 rue 7 . pee, l985 65500 015W v02 7.5 CONTROL CHARTS 1984 CHEMICAL SEPARATION SR-90
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APPENDIX C RELEASE DATA
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l Table C-1. Liquid effluent releases (C1) from the Rancho Seco Nuclear Power Plant [SNUD (1985)]
1984 Nuclide 1980 1981 1982 1983 H 1.47 E-02" 8.35 E+01 6.46 E+01 7.43 E+01 2.97 E+02 Na 0 0 1.40 E-04 4.15 E-04 5.95 E-04 Cr 0 0 6.71 E-03 0 -
4 Nn 0 4.22 E-02 1.05 E-02 5.13 E-03 2.45 E-03
'Fe 0 3.92 E-04 2.3 2 E-03 0 0 Co 0 1.47 E-04 0 0 0 B
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 1.23 E-01 I3 0 4.70 E-03 1.3 9 E-03 6.88 E-04 1.71 E-02 1
135 1.77 E-03 1.87 E-03 I 0 0 1.27 E-04 134 6.99 E-02 1.53 E-01 Cs 1.34 E-03 4.95 E-02 9.61 E-03 136 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 As 0 6.34 E-04 1.25 E-05 0 1.45 E-03 140 3a 0 1.36 E-02 1.26 E-04 0 0 90 Sr 0 0 0 1.08 E-03 0 133 0 3.81 E-04 0 3.39 E-02 Xe 0 135 4.97 E-03 1e 0 0 1.62 E-04 0
- 1.47 E-02 = 1.47 x 10-2
96 REFERENCE Sacramento Municipal Utility District, 1985. Radiation Exoosure.
Environmental Protection Effluent and Waste Disnosal. Januarv-pgfpber 1984 Annual Renort. Rancho Seco Nuclear Generatina Station Unit-No. 1. Clav Station. California. License Number DPR-54.
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APPENDIX D ADDITIONAL PARTICIPANTS IN IIIIS PROJECT I
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The authors of this report have been the Principal Investigators on this proj ect . However, there scre many other persons who made significant contributions to this proj ect. Listed below are some of these additional persons and the area in which they contributed to this proj ec t .
Field Ssmole Collection D. K. 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. Roberts - Health and Safety Research Division, ORNL W. H. Shinpangh - Health and Safety Research Division, ORNL Samole Preparation 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.
4
APPENDIX E RADIATION UNITS USED IN THIS REPORT
103 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). Giv en bel ow 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 set of units to the other.
New SI Quantity unit and Basic SI Old unit Conversion symbol dimensions and symbol Exposure coulomb roetgen (R) 1 C kg-1 =
per kilogram, 3.9 x 103 R C kg-I Absorbed Gray (Gy) joules per rad (rad) 1 Gy = 100 rad dose kilogram, J kg-1 Dose Sievert (Sv) joules per rem (rem) 1 Sv = 100 rem equivalent kilogram, J kg-1 Activity Becquerel per second, curie (C1) 1 Bq =
(Bq) s -1 2.7 x 10-11 Ci c9 4
=
I RtPopeT Nvv6ER # Ass gaea ps T/DC saa vos Aro , <f sny)
NRC FORM 33S U S NUCLE AR REGUL ATORY COMMissiO4 (2 Set 72 [1*23 BIBLIOGRAPHIC DATA SHEET NUREG/CR-4286 SEE aNSTRUCTIONS ON THE REVERSE 2 TITLE AN0 5ustiTLE 3 LE AVE BL ANE Evaluation of Radioactive Liquid Effluent Releases from the Rancho Seco Nuclear Power Plant 4 D ATE REPORT COYPLETED MONYM TEAR 5 ^v rHoRa' December 1985 a o^' E RE POR T i5SL ED C. W. Miller, W. D. Cottrell, J. M. Loar, J. P. Witherspoon l March 1986 7 PE RF ORMiNG ORG ANI2 AT ION N AME AND MalltNG ADOR E S$ Hartwee le Lodet 8 PROJECT T A5m WORM LNi T NUMBER Uak Ridge National Laboratory '""'**"'""""
Health and Safety Research Division P. O. Box X Oak Ridge, TN 37831 A9468 10 SPONSORING QFtG ANel Af iQN N AVE AND W Att rNG ADORg $$ (pngsug. f.p Codes i t. T vPE OF REPOR T Division of Pressurized Water Reactor Licensing-B Technical Office of Nuclear Reactor Regulation o ,E R Oo CO, E R E D u.... ,,,,,,,
U.S. Nuclear Regulatory Commission Washington, DC 20555 12 SUPPLEME N T AR Y NOT t5 13 A85TR ACT f1N eoras or 'ess)
A project has been carried out by Oak Ridge National Laboratory (ORNL) to estimate 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 5 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 frc n ORNL during November and December of 1984 to conduct an environmental sampling program around the site. Elevated levels of some 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 contaminated water and soil around the RSNPP. The ingestion of fish is the single most important pathway identified in this analysis.
14 DOCUYE NT AN AL Y5i5 - a R E *WORUS DESCR+PT OH5 'S Av AitasitiT v nuclear power plant contamination sTATEvENT pressurized water reactor environmental measurements liquid wastes dose radionuclides Rancho Seco MMv@5fdCar,0%
) ,T.,
o lenti..E R5 0,EN ENcE D TiRvs Unclassified a r .. .,,
Unclassified t 7 NVYBER v> P AGES td PR CE
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