ML20245C299
| ML20245C299 | |
| Person / Time | |
|---|---|
| Site: | Fort Saint Vrain  |
| Issue date: | 12/31/1988 |
| From: | COLORADO STATE UNIV., FORT COLLINS, CO |
| To: | |
| Shared Package | |
| ML20245C297 | List: |
| References | |
| NUDOCS 8904270103 | |
| Download: ML20245C299 (130) | |
Text
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FORT ST. VRAIN
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1 x - l PROGRAM i
SUMMARY
REPORT 1988 ! l COLORADO STATE UNIVERSITY FORT COLLINS, COLORADO 80523 8904270103 890420 PDR ADOCK 05000267 R PDC 8
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7 1 I RADIOLOGICAL ENVIRONMENTAL'MONIf0 RING PROGRAM
.l, For the Fort St. Vrain Nuclear Generating Station Operated by the Public Service Co. of Colorado Sumary . Report i for the Period January 1,1988 - December 31, 1988 Prepared by: / M./ '
d !/'/ / f; 1 Dames E. Johnson, Professor date Colorado State University
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Reviewed by: a v -[ /f
- Superintendent't of Chemistry ' bate' l
and Radiation Protection Reviewed by: k m,,tL\ d , NAA".ib a u-19-v9 Radiochemistry Supervisor ' Date Approved by: _ _ [ao[s't ' Nuclea[ Support Services Manager Date 1 4 59 I i
y U. > 1, , Acknowledgements , Many persons have contributed to this project during 1988, and it is .fmportant. to acknowledge their effort. We'also wish to thank the citizens from whose farms, homes, and ranches we collect the environmental samples. Without their cooperation the project would not be possible.' The persons' working directly on the project have been: i Joseph Bianconi Graduate Research Assistant Deborah Blunt Graduate Research Assistant , John Fleming Student Employee Roger G rdes Undergraduate Student
; Patti Kelley Student Employee Grant T. Reid Programmer Charles Sampf er Chief Electronic Technician l David Thorne Graduate Research Assistant .
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! James E. Johnson Professor and Project Director p.
Azw% Sharon Clow Laboratory Coordinator l' t
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TABLE OF CONTENTS Page No. Acknowledgments 11 l List of Tables iv List of Figures vi I. INTRODUCTION 1
.,., II. SURVEILLANCE DATA FOR 1988 AND INTERPRETATION OF RESULTS 6 A. External Gamma Exposure Rates 6 B. Air Sampling Data 9 i C. _ Water Sampling Data 34 D. Milk Data 67 E. Food Products 79 I
l F. Aquatic Pathways 81
.i
. G. Sample Cross-check Data 84 H. Summary and Conclusions 93 I
l III. ENVIRONMr.NTAL RADIATION SURVEILLANCE PROGRAM AND SCHEDULE 112 1 IV. APPENDIX 131 i ! i A. Survey of Dairy Farms 131 ) i J
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LIST OF TABLES Page No. l II.A.1 Gamma Exposure Rates. 8 II.B.1 Concentrations of Long-lived Gross Beta Activity in Airborne Particles. 11
- a. First Quarter, 11
- b. Second Quarter, 12
- c. Third Qua:ter, 13
- d. Fourth Qutrter, 14 II.B.2 Tritium Conce strations in Atmospheric Water Vapor, pCi/L. 18 I
- a. First Quarter, 18
- b. Second Quarter., 19 l
- c. Third Quartgr, l 20 t
.i'
- d. Fourth Quarter, 21 II.B.3 Tritium Concentrations in Air, pCi/m3 22 s
- a. First Quarter, 22
- b. Second Quarter, 23
! c. Third Quarter, 24 I
- d. Fourth Quarter, 25 l
. II.B.4 Tritium Released in Reactor Effluents. 26 II.B.5 I-131 Concentrations in Air. 29
- a. First Quarter, 29 j b. Second Quarter, 30 1
- c. Third Quarter, 31
- d. Fourth Quarter, 32 II.B.6 Radiocesium Concentrations in Ambient Air. 33 II.C.1 Cross Beta Concentrations in Bi-weekly Composites of Drinking Water. 37 l
I 1
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. LIST OF TABLES (Continued)
Page No.. II.C.2 Tritium Concentrations in Bi-weekly Composites of Drinking Water. 38 5 II.C.3' Radionuclides Concentrations in Bi-weekly Composites 4 of Drinking Water. 39
.{ II.C.4 Tritium Concentrations in Surface Water. 50 1 . ..
j-II.C.5 Radionuclides Concentrations in-Surface and Effluent Water' 52
.g.
II.C.6 Radionuclides Concentrations in Ground Water. 65 j, Ll II.C.7 Tritium Concentrations in Ground Water, 66 L I
'l i II.C.8 Maximum Permissible Concentrations in Water. 66 l
-p' II.D.1 Radionuclides Concentrations in Milk. 70 II.D.2 Tritium Concentrations in Milk. 77
.. II . E.1 Radionuclides Concentrations in Food Products. 80 .
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<.T II.F.1 Radionuclides Concentrations in Fish. 82 3 II.. 2 -Radionuclides Concentrations in Sediment. 83 i 1 II.G.1 EPA Cross-check Data. 88 a II.G.2 Tritium Concentrations in Cross-check Data, j' CSU-Colorado Dept. of Health-PSC. 90-p II.G.3 Gross Beta Concentrations in Water Cross-check Data, f CSU-Colorado Dept. of Health-PSC. 91 J II.G.4 Intralaboratory Cross-check Results. 92 II.H.1 Data Summary. 100 j II.H.2 Geometric Means of Selected Sample Types 1985-1988, 107 1 III.A.1 Radiological Environmental Monitoring Program. 114 III.A.2 Detection Capabilities for Environmental Sample Analysis, LLD. 116 III.A.3 Reporting Levels. 117 l III.B.1 Sampling Locations for Environmental Samples. 118 l 129
.[ III.C.1 Land-use Census, 1988.
! V
LIST OF FIGURES Page No. Figure II.B.1 Gross Beta Concentrations in Air 15 Figure II.C.1 Tritium Concentrations in Water 1974-1988 51 Figure II.D.1 I-131 Concentrations in Milk at Site A.22 76 Figure III;B.1 Close-in Sampling Locations 127 Figure III.B.2 Adjacent and Reference Sampling Locations 128' Figure III.C.1 Land Use Census, 1988 130 h t 5 e I i i 1 J v1 ) _ _ _ _ _ _ _ - - _ _ - - _ . - _ _ - - - - - - - - _ - - - - - . - - - - - - - - - - _ - - _ - - - - - - _ _ _ - - - - - - _ - - - - - - . - - - - - - - - - - - - - --_-- - - - - - - - - - - . - - - - - - - -- J
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1 I i Il Introduction to Radiological Environmental Monitoring Data for ) l
. the Period January 1,1988 - December 31, 1988 I 1 )
j During 1988 the Fort St. Vrain Nuclear Generating Station produced ) I thermal energy as follows: Dates with Thermal Gross Thermal Energy Month Energy Generation Production (MWH)
;)
Jan. 1-31 402,863 i Feb. 1-10 100,788 i 12-29 139,596 i Mar. 1-31 455,973 ; Apr.
,} 1-7 61,530 i 21-30 99,147 i May 1-6 88,111 l 18-31 73,962 June 1-30 458,144 July 1-5 74,262 Aug.-Dec. 0 0 1
l Total for 1988 1,954,378 l A complete and detailed listing of radioactivity released by all effluent routes may be found in the Public Service Company of Colorado I Semi-annual Effluent Release Reports for 1988 to the U.S. Nuclear i
! Regulatory Commission. When possible in this report, any correlation of radioactivity in environmental samples with the effluent release data is discussed. These discussions are presented in the appropriate . sample type section and in the summary section, II.H.
Table III.A.2 lists the LLD values achievable by the counting systems used during 1988 on project samples. These values are given for typical sample sizes, countir.g times and decay times. The LLD is, therefore, an a priori parameter to indicate the capability of the detection system used. The LLD values in Table III.A.2 were calculated
, as suggested in NUREG-0472.
I
2 em Throughout the report, however, when a sample result is listed as less.than a specified value, that value is the calculated MDC (minimum detectable concentration). This approach is analogous to that of Currie (NUREG/CR-4007): the MDC is the same as c S , the critical signal, and the LLD is equal to SD , the detectable signal. The MDC value applies to the actual sample size, counting time and decay time applicable to that individual sample. It is calculated as: MDC = 2.33 e8 /E Y V E- At Where: eB = Standard deviation of background count rate E = Counting efficiency, c s-1 pCi-1 Y = Chemical yield V = Sample mass or volume A = 0.693/ Half-life t = Decay time between sample collection and analysis This calculation method assumes that E and Y are constants and makes no allowance for systematic error. It should be noted that we have not used the notation < MDC for values less than MDC. Rather, we report the result as less than the actual MDC value. Because the MDC is dependent upon variables such as the background count time and sample size, the value will be different for each sample type and even within sample type.
! Essentially all radioactivity values measured on this project are near background levels and, more importantly, near the MDC values for each radionuclides and sample type. It has been well-documented that environmental radioactivity values exhibit great inherent variability.
I This is partly due to sampling and analytical variability, but most i I l - - - - _ _ _ _ _ _ _ -
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3
. importantly due to true environmental or biological variability. As a l result, the overall variability of' the surveillance. data is quite large, )
4 j and it is necessary to use mean values from a rather large sample population size to make any conclusions about the absolute radioactivity concentrations in any environmental pathway. a j Environmental radiation surveillance data also commonly exhibit l non-normal frequency distributions. Usually the data can be l j satisfactorily treated using log-normal statistics. However, when the i . 8 number of observations is small, i.e., less than 10, log-normal treatment is tentative. The geometric means and geometric standard i deviations are calculated for each sample set. If any data ' point measured resulted in a negative value, the corresponding MDC is used in the calculation of the log-normal statistics. (Negative values are
'I ! possible due to the statistical nature of radioactivity counting.) In Section II.H. Conclusions and Summary, the geometric means and geometric standard deviations for the reporting period of 1988 are listed in Table a
I II.H.2. . i The arithmetic mean for each sample set is also listed in Table l II.H.2. All measured values, both positive and negative, are used in i
! the calculations of the arithmetic mean. This is the suggested practice l
' by Gilbert (Health P.hysics 40:377, 1984) and the NRC (NUREG/CR-4007).
^
Many sets of data were compared in this report. The statistical i
! test used was either a "t"-test or a paired "t"-test. If data sets are noted to be significantly different or not significantly different, the confidence for the statement is at the 95% level (a = 0.05).
In this report we have footnoted appropriate tables with the maximum permissible concentration applicable to each radionuclides. We
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p $ .i .g* I'"esa - a=p8(4My ' ~ have chosen to list the maximum permissible concentrations as found in Appendix 8 Table II of 10CFR20. This is the concentration in water or air of each radionuclides which if ingested or inhaled continuously would singularly produce the maximum permissible radiation dose rate to a specified individual member of the general public. That value is 500 mrem / year, but must include the dose from all possible sources, and, therefore, cannot be solely due to reactor effluent. ' As stated in
! 10CFR20 these are the maximum concentrations above natural background that a licensee may release to an unrestricted area. It is assumed that ; no direct ingestion or inl;alation of effluents can occur. at the t
restricted area boundary and that dilution and dispersion decreases the i' concentration before it reaches nearby residents. This is certainly the case for the Fort St. Vrain environs.
! There is no specified maximum permissible dose rate or dose commitment for residents near the Fort St. Vrain reactor from the reactor effluents. Such limits for water cooled reactors are found in 10CFR50 Appendix I. These are judged as "As Low as Reasonably -
Achievable" dose rates from such reactor types and, although not directly applicable to the Fort St. Vrain gas cooled reactor, can be used for comparison purposes. A limit that does apply is the independent maximum permissible dose commitment rate set by the E.P.A. (40CFR190) for any specified member of . the general public from any part of the nuclear fuel cycle. This value is 25 mrem / year, the dose rate to the whole body from all contributing radionuclides excluding background and medical radiation dose rate. e i 1
s . 5 Dose commitments are calculated for hypothetical individuals for any mean concentrations noted in unrestricted areas that are significantly above control mean values. The following is the footnote system used in this report.
- a. Sample lost prior to analysis,
- b. Sample missing at site.
- c. Instrument malfunction.
- d. Sample lost during analysis.
- e. Insufficient weight or volume for analysis,
- f. Sample unavailable.
- g. Analysis in progress.
- h. Sample not collecte'J (actual reason given).
- 1. Analytical error (actual ~ reason ~given).
N.A. Not applicable. s 6 l! lI i t l L___._ _ __ _ _ _ _ _ _ . _ _ _ _ . _ _ _ _ . _ _ _ _ _ _ _ _ _ . _ _ _ _ _ _ _ _ _ . _ _ _ _ _ _ _ . _ _ _ . _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _
6
.. l l II. Surveillance Data for January Through December 1988 and a Interpretation of Results A. External Gamma-ray Exposure Rates The average measured gamma-ray exposure rates expressed in mR/ day are given in Table II.A.1. The values were determined by CaF2:Dy g (TLD-200) dosimeters at each of 41 locations (see Table III.B.1). Two 1 i
- TLD chips per package are installed at each-site and the mean value is-l1 reported for that site. The mean calculated total exposure is then li divided by the number of days that elapsed between pre-exposure and post-exposure annealing to obtain the average daily exposure rate. The TLD devices are changed quarterly at each location. Fading.during field l exposure is minimized by the post-ar.nealing readout procedure.
1 The TLD data indicate that the arithmetic mean measured exposure rate in the facility area for all of 1988 was 0.36 mR/ day. The mean t exposure rate was 0.36 mR/ day for the adjacent area and 0.34 mR/ day for ihereferencearea. These mean values were not significantly different from each other. The exposure rate measured at all sites is due to a combination of exposure from cosmic rays, from natural gamma-ray emitters in the earth's crust and from ground surf ace deposition of fission products due
.l to previous world-wide fallout. The variation in measured values is due to true variation of the above sources plus the variation due to the ~
measurement method. The purpose of the two TLD rings around the reactor i is not to measure gamma-rays generated from the reactor facility itself, but to document the presence or absence of gamma-ray emitters deposited j- upon the ground from the reactor ef fluents. Since the inception of
! power production by the reactor, there has been no detectable increase
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__.*____-__ma. _ _ _ _ _ _-_--__um___-______--_.___-_--__m._.--m.a_._--__-2m_.-m __m_--um.ha-m. A emA Asuub.a h 4 A 29 F?dI*__
7 in the external exposure rate due to reactor releases. Fallout, both from the Chinese nuclear weapon tests and from the Chernobyl accident, was detected in the past. The TLD system was calibrated by exposing chips to a scattered gamma-ray flux produced in 'a cavity surrounded by uranium mill tailings. This produces a gamma-ray spectrum nearly identical to that from natural background measured in the reactor environs ~. . The quality control
.I L J- program includes calibration before readout of each quarterly batch of l! TLD devices.. .p For comparison purposes, the EPA in EPA 520/5-88-057 Report #53' lists 0.38 + 0.11 mR/ day for the background external exposure rate in Denver. }l J-lk 4
w k i l ; i-5 _ _w--_xma_____-,___,-_---_---- --_a-----u---_ _ - - - -- - - - , - - - _ - - - - - -___ _ --._---.------_-_-----.s--_ u_------- - -----_---.--a-..------. _.--- - - - - - - - _ - - __.._ _-------_ - - - - -
f
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. 8
**! - Table II. A.1 Gamnraa Exposure Rates. (mR/dsy) If'S g
[ r Facility Area 1st Quarter , 2nd Quarter 3rd Quarter 4th Quarter - F-1 0.35 0.43 0.42 0.44 F-2' O.33 0.40 0.36 0.46 F-3 0.37 0.36 0.37 0.42' - F 0.32 0.35 0.43 0.37. F-5 .0.36 0.39 0.37 0.38 F-6 0.30 0.32 0.35- 0.36 F-7 0.30- 0.37- 0.35 0.38 F 0.34 0 33 0.40 0.41 F-9 0.43 0.30 0.37 0.41 F-10 0.34 0.37 0.38 0.39 F-11 0.34. 0.34 . 0.41 0.46 - , F-12 0.30 0.31 0.40 0.44 F-13 0.31- 0.25 0.33 0.37
, F-14 0.33. 0.20 0.34 0.39 ~~
F-15 0.32 0.35 0.34 0.35 F-16 0.33 0.35 0.36 0.43 F-17 0.37 0.36 0.39 0.35 F-18 0.33 0.39 0.44 0.41 i IC(1.96o)- C.34(0.062) 0.34(0.11) 0.38(0.06) 0.40(0.069) I Adjacant Area 1 A 0.30- 0.42 0.40 0.36
]
A-2 0.34 0.38 0.39 0.43 A-3 0.31 0.41 0.37 0.42
.l
-A-4 0.32 0.36 0.38 0.36
.l A-5 , 0.36 0.36 0.38 0.34 A-6 0.35 0.31 0.37 0.35
' 0.44 A-7 0.31 0.36 O.38 A-8 0.32 0.45 0.41 0.41 .
I A-9 0.37 0.38. 0.39 0.42 A-10 0.33 0.42 0.41 0.47 l A-11 0.33 0.35 0.37 0.39
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A-12 0.33 0.32 0.32 0.41 0.31 0.31 0.34 0.35
].;
A-13 A-14 0.34 0.30 0.34 0.38 A-15 0.35 0.28 0.36 0.36 A-16 0.34 0.23 0.36 0.40 l-
- A-17 0.34 0.28 0.38 0.42 l1- A-20 0.36 0.38 0.42 0.46 0.33(0.039) 0.35(0.11) 0.38(0.05) 0.39(0.077)
X (1.96o) Reference Area l R-2 0.30 0.29 0.34 b R-3 0.31 0.36 0.35 0.40 R-4 0.29 0.33 0.31 0.36
-l- . R-5 0.27 0.37 0.33 0.37
' 0.33 0.42 1 R-7 0.28 0.40 i 0.29(0.031) 0.35(0.082) 0.30(0.03) 0.39(0.052)
X (1.96o-) 1
; b1 TLD packet removed from pole by vandals.
'l.. 9
'!!.B. Ambient. Air Concentrations
) 1. - Gross Beta Activity ll.
l a-
.The air concentrations of long lived particulate gross beta j activity measured at he facility.and reference sampling sites are
^
( listed in Tables II.B.la-id for each quarter of 1988. A-19, while technicrily in the adjacent zone, is only a few meters from the facility. l [ l boundary and logically should be considered a facility site. It has '- l] been termed a facility site since the inception of the monitoring program. The reference sites R-3, R-4, and R-11 are all new locations 1.
, as of January 1,1984 and.sufficiently distant to be considered
- )
1 reference (control) locations. (See Table III.B.1), s j The reported concentrations are listed in units of femtocuries per q .. A cubic meter of ambient air, although tne measured activity is due to a 1 combination of radionuclides almost all of which are naturally l ' occurring. It should be noted that the current technical specifications-no longer require measurement of gross alpha activity. All filters,
- i. =
- j. however, are saved indefinitely for later alpha activity analysis if 1
j needed. [ The mean gross beta concentration in air for all facility stations r 3 i for all of 1988 was 26 fCf /m . The mean concentration for all 3 references stations was 24 fCf/m . This slight difference was 2 statistically significant at 95% confidence level but not significant at ' i
; 97.5% level. In any case the slight difference was not due to reactor j effluents because specific fission product concentrations, e.g.137Cs,
- )
were not statistically higher in the facility area. Any real difference i was due to naturally occurring radionuclides. There was also no d i 1 evidence of fission product or activation product debris in surface air '
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' ^ ' ' from the: reentry of COSMOS 1900. .The U.S.S.R. satellite was predicted j to reenter the earth's atmosphere between mid September and early j.
, October 1988. .
The gross beta data for 1988 have been added to the plot of air concentrations observed since 1973 (Figure II.B.1). In this figure the { half-yearly mean values for the facility sites are plotted with the-i values from the reference sites. The contribution from Chernobyl is " clearly evident in 1986. It can be observed that overall mean values j are not significantly different and that world-wide fallout, principally due to Chinese atmospheric nuclear weapon tests, is the predominant j contributor to the measured values over the period shown. 1 i There has never been a significant difference observed between ' facility and reference sites. Thus, it can be again concluded that 1' reactor air effluents of particulate fission. products or activation products are not a source of dose commitment for the Fort St. Vrain
,. environs population.
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l .. 15 Figure II.B.1~ l 1000 - Gross Beta Concentrations in Air 900 - 800 - 700 -
- W Facility Sampling Stations .
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- 2. citium Activity Atmospheric water vapor samples ~are collected continuously by passive absorpt'on on silica gel at all seven air sampling stations (four in the facility area and three in the reference area). The specific activity of tritium in water extracted from these weekly samples for 1988 is listed in Tables II.B.2a-2d. The corresponding tritium concentration in air (pCi/m3) is calculated from the specific ~
activity data using weekly mean temperatures and dew points measured at the FSV meteorological tower. The measuring point is at a height of 2 m from the surface. The tritium air concentrations are shown in Table l II.B.3a-3d. i The principle release mode of tritium from the reactor is batch liquid releases from holding tanks (system 62). The tank water is first j- analyzed and then released with sufficient additional dilution, 'f i necessary, to not exceed 10CFR20 concentration limits. The summary of tritium release by all modes is shown in Table II.B.4. The summary f ndicates that the total tritium released in 1988 was 2.8 times greater , 4 l than in 1987 for all routes. (See 1987 annual report to the USNRC). Ei This effluent release was detected principally at two of the air l sampling sites. f
! Sampling locations F-16 and A-19 are located near the Goosequill Ditch, which is the common rout'e for liquid effluent tritium release.
Tables II.B.2a-2d indicate a strong correlation of elevated atmospheric tritium concentrations corresponding to the batch release of tritium in water along the ditch. Due ;o evaporation while in transit, elevated tritium concentrations in air have been observed for these two locations
! often in past years. The concentrations observed, however, have always f
L l l.:
4# 17 i been below the limit of regulatory concern. The occasional elevated values at the reference sites are assumed to be statistically false l
, positive values.
The mean value for sites F-16 and A-19 were significantly greater ) l l than for all other sites during the year. When all four facility sites j are averaged, however, the total mean value was 470 pC1/L. The mean for the three reference sites was less than the MDC value of 250 pCi/L. Tfie~ mean for the facility stations was significantly greater than the mean i
~ (
l for the adjacent stations. Radiation dose commitment estimates are not j warranted on the basis of elevated air concentration values alone. Inhalation is not a significant pathway for dose to humans. The milk j and food product pathway is the only significant source of radiation l dose to humans from environmental tritium. See results for these j pathways ili sections II.D and II.E. Since the same relative humidity is assumed for all sites, Table s II.B.3 shows the same site dependence on reactor effluent as Table II.B.2. Only the units used to measure tritium in surface air are - different. 1 I k e 4
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)
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)
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)
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/
b t / / / / / / / / / / / / / G a a 0 0 0 0 0 1 1 1 1 2 2 2 2 2 0 T D 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 I j1{ { ! I j ; 2' , j ;!i j i : :
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,, t F 1 1 c F I1' l!IIlII II I 1Ill a E e -
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. b IlI a 5
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)
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~ M nii sti se u L ibd) hacd) hat ok A t rl p ceal p ces ec i
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- IltI Ili1 l
4 4 27 H
- 3. Concentrations of Gamma-ray Emitting Radionuclides in Ambient Air Tables II.B.Sa-Sd list'the concentrations of I-131 in air as measured by activated charcoal sampling and Ge(Li) gamma-ray spectrum analysis. Each sample from the seven air sampling stations is counted-within 96 hours after collection. A 100 minute count and a sample volume of 800 m3 is required to achieve an MDC of 33 fCi/m .3 . Radon daughters and Thoron daughters are trapped on the particulate filter ahead of the charcoal trap. Radon-222 daughter in-gro *n the charcoal does not provide interference to the region of Interest for I-131 using the Ge(Li) high resolution spectrometry. Any positive I-131 activity is corrected for radioactive decay back to the midpoint of the collection period. Decay correction to the midpoint of the sampling period is appropriate as any I-131 in air would not arrive at the sampling stations at a constant rate, but rather in pulses of short duration compared to the collection period. This is the case whether the I-131 source term would be weapons testing fallout or reactor stack ef fluent. i There were only occasional positive values very near the MDC value and all are assumed to be false positives. 1-131 concentrations due to reactor effluent have never been detected in any sample type in the Fort 1
St. Vrain environs. L Table II.B.6 lists measured ambient air concentrations of Cs-134 and Cs-137. These values are from gamma-ray spectrum analyses on weekly air filters composited quarterly from each of the seven air sampling stations. The occasional positive Cs-137 concentrations measured are likely due to resuspension of surface soil. The Cs-137 activity is due i !
! l
'** 28-1 . ..
L '
. to Chernobyl (or previous) fallout which is bound by clay minerals on -
the' surface of undisturbed soil. For the entire year, the mean of the ( facility stations was not different from the mean of.the reference
' stations.
)\ .
Although only Cs-134 and Cs-137 are reported, each gamma-ray f spectrum is. scanned for.. evidence of peaks from other fission products and activation products. Normally only gamma-ray activity due to the - naturally occurring background radionuclides are observed. During the
. second quarter of 1986, however, many other radionuclides were observed due to the Chernobyl accident. Of these only Cs-137 can still be.
i detected. L i t s t-i
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)
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- 9 1 3 3 0 5 0 0 R 5
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) ) )
s n s 0 1 1 o e 1 1 6 9 2 2 2 i t t i 9 . E. ( ( ( a S - 2 2 2 2 1 r F 9 1 4 t y < < < < < . 1 2 1 n t ) e i s c l n i c o c it a s C 4 4 2 2 il F 6 8 3 2 a _ m 7 . l u - 1 1 3 3 1 1 1 1 s
._ i F s < < < < < < < < g
_ e n c it o e n d 4 7 4 7 4 7 4 7 u i d oi 3 3 3 3 3 3 3 1 3 1 o c 1 1 1 a il 1 1 1 R d c - - - - - a u s s s s s s s s t o 6 R n C C C C C C C C o _ n u B. o D ( i I I t r r r r 8 ce e e e e o _ e 8 et t t d t d t h t l 9 l a s r n r r r t r 6 l D 1 a 2 a 3 a 4 a 9 b 1 u u u u T a C o Q Q Q Q 1 ! l 1
.O -7 ,
il . <; _ II .C.- Radionuclides Concentration in Water
- 1. Drinking Water Drinking water is sampled weekly and composited biweekly at two c locations. Location R-6 is the well used for' drinking water by the town i of Gilcrest, Colorado, and R-3 is a water tap located on the CSU dairy i farm. The Gilcrest well is the nearest public water supply that could i
i be affected by the reactor effluents. R-3 samples are from the Fort ' Collins drinking water supply and serve as a reference location since I its source is run-off surface water from the Rocky Mountains to the
! West. However, water treatment systems for the two water supplies are i
} very different.
Table-II.C.1 shows gross beta concentrations measured in 1988 from j each water supply. The mean for the Gilcrest site was again f i significantly higher than the Reference site in Fort Collins. This is only due to the different water treatment practices. The city of kiilcrest does not filter its water -and natural radionuclides i concentrations are responsible for the higher measured concentrations. . i As can be observed in Table II.H.2, the mean for the entire year for the Gilcrest site was not greater than in previous years. i Table II.C.2 lists measured tritium concentrations in these same
! two drinking water sources. The yearly arithmetic mean value for the Gilcrest location was greater than MDC. The mean yearly concentration f measured in the Gilcrest supply was statistically greater than in the Fort Collins supply. The difference, while very small, can be used to estimate a radiation dose commitment to the Gilcrest population for the
. period. Assume the following:
I I 1 j
E
].c g. ,
l.
- 1. The critical individual is an adult.
2.. The average annual- intake of tap water is 388 ml/ day (ICRP-23).
- 3. The mean concentration for Gilcrest residents during the l- year is the measured difference between the two potable water sources, i.e. 370-120 = 250 pCi/L.-
~
Therefore by ICRP-26,30 dose commitment methodology the weighted committed dose equivalent rate, A, is calculated as:
- 2 H = (250 pCf)(0.39 L)(365 d)(0.037 Bq)(1.7x10~1ISv)(10 rem) y.
L day pCi Bq Sv 1
, 2.2x10-6 rem , 2.2x10-3 mrem y y
.r (For a 5-14 year old child the weighted committed dose equivalent rate would only be 1.10x10~3 mrem /y) .
s This committed dose rate would still be trivial in absolute. terms and , certainly is when compared to background dose rates of approximately 300 mrem / year as calculated by the same methodology. Since 3H was not detected in milk or other foods, intake of water from these sources is i not included. The EPA limit for community drinking water systems is 20,000 pCi/L
. for tritium. Figure II.C.1 shows tritium concentration in Gilcrest drinking (potable) water source.
i
-[ . The two drinking water supplies are also analyzed for fission
'l product and activation product concentrations. A sample of 18 liters is passed through Dowex 1-x8 anion exchange resin and the resin then i
f .,: .d - ' L. , ?- ' 36 y
. counted by Ge(Li) spectrometry for I-131. A three liter aliquot of the . .
original sample is counted directly for the' other gamma-ray emitters.
. , . Inspection of Table II-C.3 reveals occasional positive values of radionuclides concentration, but with the exception of Cs-137, these are interpreted to be random variations. The Cs-137 is the' residue from the 1986 Chernobyl accident fallout as well as from past world-wide fallout from nuclear weapon testing.
L-b a I iI I -
!.o Table !!.C.1 Gross Beta Concentrations in Biweekly Composites of Drinking k'ater. (pC1/L) l Collection Gilcrest City R-6 '
Fort Collins City R-3 l Date 1988 (Reference) i 1/2 & 1/9 7.7 (2.5)
- 1.1 (0.58) 1/16 & 1/23 5.5 (2.5) 0.78 (0.56) 1/30 & 2/6 7.2 (2.5) 0.46 (0.54) 2/13 & 2/20 9.4 (2.6) 1.8 (0.61) 2/27 & 3/5 6.7 (2.5) 0.84 (0.56) i 3/12 & 3/19 4.3 (2.4) 0.59 (0.56)
'l 3/2684/2 8.1 (1.9) 1.3 (0.59) , j 4/9 & 4/16 7.5 (1.8) 1.1 (0.45) 4/22 & 4/30 7.3 (1.8) 2.0 (0.43) 5/7 & 5/14 6.8 (1.9) 1.1 (0.44) i 5/21 & Sf D 8.7 (2.6) 0.92 (0.57) 6/4 & 6/11 5.6 (2.4) 0.90 (0.57) 6/18 & 6/25 5.4 (2.4) 0.99 (0.57) y 7/2 & 7/9 5.5 (2.4) 1.0 (0.57) l 7/16 & 7/23 9.1 (2.6) 0.99 (0.57) 7/30 & 8/8 5.9 (2.5) 0.65 (0.55) j 8/13 & 8/20 8.0 (2.6) 0.97 (0.57) 8/27 & 9/3 3.0 (2.3) 1.1 (0.57)
} 9/10 & 9/17 6.5 (2.5) 1.2 (0.58)
I 9/24 & 10/1 7.1 (2.5) 1.1 (0.58) 10/8 & 10/15 7.4 (2.5) 0.99 (0.57)
! 10/22 & 10/29 9.0 (2.6) 0.92 (0.57)
- 11/5 & 11/12 5.7 (2.5) 0.91 (0.57) 11/19,a 11/26 7.8 (2.5) 1.1 (0.57) 12/3 & 12/10 7.1 (2.5) 1.1 (0.58) 12/17 & 12/24 5.5 (2.4) 1.3 (0.59)
I i
- 1.96 e (Due to counting statistics.)
l - 1 I
- j. .
L. . - 38 i Table II.C.2 . (pC1/L)
" Tritium Concentrations in Biweekly Composites of .Orinking Water.
4
! Collection Gilcrest City R-6 '
Fort Collins City R-3 l' Oate 1988 (Reference)
! 1/2 & 1/9 350 (360)* < 300 1/16~& 1/23 < 290 < 290
< 290 l 1/30 8.2/6 450 (310) i 2/13 & 2/20 370 (270) 340 (270) 2/27.& 3/5- 230 (270) 380 (270) ,
l 310 (310)
- j. 3/12 & 3/19 610 (MO) 3/26 & 4/2 560 (280) < 230 4/9 & 4/16 490 (310) < 230 4/22 & 4/30 890 (310) -240 (280) ,
5/7 & 5/14 350 (310) < 260 5/21 & 5/28 530 (310) < 260 2 6/4'& 6/11 < 250 < 250 6/18 & 6/25 < 250 < 250
. 7/2 & 7/9 : 250 < 250 j 7/16 & 7/23 < 250 < 250 7/30 & 8/6 < 250 < 250 i
8/13 & 8/20 < 250 < 250
- ! 8/27 & 9/3 340 (370) < 250 i 9/10 & 9/17 280 (370) < 250
! 9/24 & 10/1 < 260 < 260 10/8 & 10/15 < 250 280 (370) 10/22 & 10/29 870 (380) 590 (380) 11/5 &.11/12 830 (340) 470 (340) 11/19 & 11/26 800 (340) 720 (340) 12/3 & 12/10 960 (340) 660 (340) l -
12/17 & 12/24 640 (320) 600 (320) i .
- 1.96 o (Due to counting statistics.)
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n r i < < < < < < < < < < < i o G f s n s o i n ) t i 6 a l 7 r g l 1 2 1 9 2 2 2 8 0 1 0 2 t n o3 . ( 2 3 2 2 n i C - 0 1 2 1 1 1 1 e d R 7 c n t < < < < < < < < < n e F 1 ) . o s C s8 c k8 it e e/
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l / s 4 s c o2 e 4 1 1 6 1 1 1 3 8 1 1 6 u w1 r6 ( . . ( ( . g n t c - 0 1 2 1 1 1 2 3 3 n o l R 2 5 8 it i r i < < < < < < < < < n d o G 2 5 1 u a f o R c 3 e t o d n i o C. o l u I i c D I t e u ( ct n 4 7 0 0 e ea o 1 3 3 5 9 F 8 5 4 5 5 6 9 5 0 6 4 4 1 o l lD i 3 1 1 9 1 b l d 1 - - - - - - - - - - - G a o a - s s r b o n n e o a a 0 T C R I C C 2 N C M ~_ F C B L 1 rl[ll1ii
- +*
48 i I
- 2. Surface Water Surface water is collected monthly from four sites. Since the d reactor water effluent can be directed to either river course, there are i upstream and downstream sampling locations on both the St. Vrain Creek and on the South Platte River. ,
; Table II.C.4 shows tritium concentrations measured during 1988 at i
the four surface water sites. Most of the values were less than MDC. ' i
; The arithmetic mean value for the downstream locations in 1988 was not significantly different from the two upstream locations (Table II.H.2).
j In fact the mean values were identical . The EPA lists 300 + 200 pCi/L j for tritium measured in a Platte River sample collected on 1/4/88 for j comparison purposes. Table II.C.5 shows measurements of fission product and activation product concentrations in surface water samples collected monthly.
. There were occasional positive values,'but the mean of the downstream bites was not significantly different from the mean of the upstream sites during 1988 for any of the gamma-ray emitting radionuclides measured. This has been the case since the inception of reactor operations at the Fort St. Vrain site. The occasional positive values are either fallout Cs-137, which can be expected, or values close to the iI 2
uncertainty limits and assumed to be false positives. In addition to the monthly sampling of the South Platte River and St. Vrain Creek, a continuous water sample is colleced at station A-25. An aliquot of the farm pond outlet is sampled every 80 minutes and the composite collected weekly. The weekly composites are then combined and l , analyzed monthly. The results of these samples are also shown in Tables i
! II.C.4 and II.C.S. For every month there was evidence of measurable
}
I
S
.- 49 tritium release (see Table II.C.4). Mean values for the other
- radionuclides were less than MDC except for Cs-137. The correlation of i
the tritium concentrations with the effluent release report is high. k i t I l s e i f 1 l l 1 l l I 1 d__m___._ . _ _ _ . . . . - _ -
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- 3. Ground Water-9 Ground water is sampled quarterly at two locations. . These are at F-16, a well on1the farm inrnediately north and the closest to the .
reactor down the hydrological gradient, and at R-5, the Ehr.lich feedlot.
. Table II.C.7 lists the measured concentrations of fission products and activation products in ground water. The.Cs-137 results are not j surprising-due to residue of Chernobyl fallout, and the other results
- j- above MDC are assumed to be statistically false positive values'.
- l. For comparison purposes, Table II.C.8 lists the Maximum Permissible
-l: Concentration values in' drinking water for each of the radionuclides listed in Tables II.C.4-7.
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4 66 ! 1 i Table II.C.7 Tritium Concentrations in Ground Water q 1988. Facility Reference F-16 R-5 3/12/88 < 280 340 (340) 6/11/88' < 220 < 220 9/24/88 < 260 < 260 1/28/89 1000 (330)* 540(330)
- 1.96 o (Due to counting statistics. )
Table II.C.8 Maximum Permissible Concentrations in Drinking Water. (10CFR20, Appendix B, Table II) 6 H-3 3 x 10 pCi/L I-131 3 x 102 pCf/L 3 Cs-134 9 x 10 pCi/L Cs-137 2 x 10 4 pCi/L 4 Zr-95 6 x 10 pCi/L Nb-95 1 x 105pC1/L 5 Co-58 1 x 10 pCi/L l 5 Mn-54 1 x 10 pCi/L 5
. In-65 1 x 10 pCi/L 4
j Fe-59 6 x 10 pCi/L 4 Co-60 5 x 10 pCi/L 4 Ba-140 3 x 10 pCi/L 4 La-140 2 x 10 pCf/L
c ) 67 11.0. Mil k The dairy food chain is the critical pathway for possible radiation dose commitment around any nuclear facility. The critical individual would be an infant consuming milk produced from cows grazing local pastures. Milk is the critical pathway for possible dose commitment to humans from environmental contamination of H-3, I-131, Cs-137 and Sr-90. For this reason milk is sampled extensively to document the presence or absence of radioactivity due to reactor operations. A three liter milk
; sample is counted for determination of Cs-137, Cs-134 and Ba-La-140. To 1 ! measure I-131 at the required LLD of 1.0 pCi/L, an 18 liter sample is j concentrated by anion exchange and the resin counted by gamma-ray spectroscopy. The method of treating the milk is modified from that of McCurdy and Mellor, Health Physics 38: 203-213, 1980.
l There are no dairies (or personal milk cows) in the facility area, 1.6 km radius. The six dairies in the adjacent area,1.6-8 km radius, were selected as they are located in the highest X/Q areas (refer to updated FSAR). The description of these locations can be found in Table III.B.1 and Figure III.B.2. The single reference location dairy, R-8, is 22.5 km West of the reactor in the least predominant wind direction. Herd management practices are virtually identical at all dairy locations. The cows in the milking herd are never on pasture but under dry-lot management typical of Castern Colorado (see Appendix).
; Table II.D.1 lists the concentrations of all radionuclides that are 1
investigated in milk samples. During 1988, elevated concentrations of I-131 were again observed only at site A-22. The source of this I-131 is from nuclear medicine thyroid therapy practice in the Denver hospitals. The releases enter the S. Platte River just North of Denver.
.68 q
A-22 dairy uses irrigation ditch water for its herd during the summer 3 l rather than well water. The ditch (Independence) receives S. Platte j water upstream of FSV. This observation was first,made in 1985 and discussed at length in the 1985 REMP suunary report. Unfortunately, A-22 dairy could not provide . milk samples during the last quarter of 1 1988 due to efforts to meet production quotas. The dairy has rejoined the program beginning in January. - During October, when milk was not available from A-22, four extra water samples were collected from the Independence Ditch at the dairy f, location. ~ The I-131 concentrations on those four dates are given below.
.L Date I-131 pCi/L + 1.96 _
10/1/88 1.4 + 0.35 t ~ 10/8/88 8.0 1 0.85 10/15/88 4.0 + 0.69 10/22/88 2.0 + 0.44 If ditch water were the only source of drinking water for the A-22 herd j during this period, it can be assumed that milk concentrations would .
-l j have been approximately the same as the water concentration. The ditch flow was stopped in November and December.
Figure II.D.1 shows the frequency and magnitude of the I-131 concentrations observed at the A-22 dairy ic recent years. The large t-
; peak observed in May and June of.1986 is of course due to Chernobyl fallout, but all other peaks are due to hospital release in Denver.
l K-natural, as measured by K-40, is extremely constant in milk. The
.l: mean literature value for cow milk is 1.5 g/L. K concentrations are i.i homeostatically controlled and independent of X intake. K-nat is i ,
\ l i measured in all milk samples as a quality control measure for the other l I ,
4 i EE____ __ _ , _.. .
)
1. 69 1 l radionuclides determined in the same sample by gamma-ray spectrometry, but K-nat concentrations are no longer reported in Table II.D.1. { Elevated tritium concentrations in milk due to reactor effluents have never been observed in the operational . period of the: reactor. .This implies the tritium from reactor effluents is not contributing any radiation iose to humans via the milk pathway. ' Tritium concentrations in milk should respond rapidly to changes in tritium concentrations of, the forage water intake or drinking water intake to the cow. This is due to the short biological half-life for water in the cow (about three days. for the lactating cow). As noted in previous reports, the reported tritium concentration in milk is the tritium in water extracted from the 4 milk. Contamination of milk samples by any radionuclides due to reactor 4 effluents has never been observed during the operational periods of Fort
- St. Vrain.
i For comparison purposes, the EPA lists a measured Cs-137
' concentration in milk from Denver as 9 + 6 pCi/L on 1/4/88..
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79 II.E. Food' Products-Food sampling locations were selected from areas possibly irrigated - by sur' face water downstream of the FSY discharge point or by well' water from the aquifer most likely' to be contaminated by seepage from the farm .- a pond. The locations of these food product collection sites are described in Table III.B.1. One sample of each principal class of food products was collected from these locations. Locations and available - - produce often chanhe due to owner needs, harvest time, harvest size, etc. Each sample is homogenized without drying immediately after - ' collection. The sample is then counted by gamma-ray spectroscopy. ,* Table II.E.1 lists the date of collection and the results for the 1988 harvest. Three of the food samples showed detectable Cs-137. from past Chernobyl fallout deposition and two showed marginal but detectable l i , concentrations of Cs-134, also from Chernobyl. The-I-131 concentration-
~
'esult r in the zucchini sample from A-30 was rechecked and conff rm'ed. _
'The result, was certainly not due to reactor effluent but probably the 4
result of the use of irrigation water from the S. Platte River. In section 11.0, concentrations of I-131 from Denver hospital use were documented in irrigation ditches off the Platte River. The gamma-ray spectra were scanned for other radionuclides, but only the naturally occurring were observed, presumab.ly due to surface soil deposits. l l f I i
- 80 Table II.E.1 Radionuclides Concentrations in Food Products (pCi/kg)
Collection Date 9/13/88 - Location Food Type I-131 Cs-134 Cs-137 A-8 CORN < 5.9 < 6.5 < 7.8 A-9 MELONS < 2.9 < 3.0 < 4.4 ? A-27 TOMATOES < 8.3 < 7.0 < 8.3 , A-28 BEANS < 18.0 < 10.0 < 12.0. A-29 ONIONS < 2.8 < 2.7 5.1 (3.9) A-30 ZUCCHINI 9.1 (11.0)* 8.3 (6.0) 16.0 (8.S) A-31 BROCCOLI < 8.0 14.0 (10.0) 10.0 (12.0) R-12 POTATOS < 2.8
< 3.1 < 3.5 ,
R-13 BEETS < 6.5 -<-4.3- -
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- II.F. Aquatic PatNways 1 Table II.F.1 shows radionuclides concentrations measured in fish i
samples collected at F-19, A-25 and R-10 on two dates in 1988. The fish
?
were collected by sh'ocking and netting and the composite sample was homogenized without cleaning and analyzed on a wet weight basis. The only two positive values were due to Cs-137, assumed to b'e due to , fall out. - Table II.F.2 shows the measured concentrations of both Cs-137 and Cs-134 in surface sediment collected at R-10, the downstream location. There was measurable activity of CS-137 clearly due to the Chernobyl I fallout. The Cs-134 results are doutbful. The cesium ions are bound nearly irreversibly by the clay miniral matrix in the sediment. i Monitoring for Corbicula fluminea, a species of freshwater clam, i . l was conducted a't all fish sampling sites. These monitoring dates 3
! coincided with the fish collection dates. Corbicula have been introouced to North America from Asia. The freshwater clams are now found in large, river systems in the U.S. from coast to coast. The l !
Colorado Division of Wildlife has stated that Corbicula have been found { in Northern Colorado at Boyd Lake, some 30 miles from the Fort St. Vrain Nuclear Generating Station. However, to this date, our s'amplings have l l indicated no evidence of Corbicula .in any of the sampling sites of the I reactor surface water courses. e l l I l l li
.- )
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- 1. d . n d
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(;/ . t t. F! Table II.F.22 Radionuclides Concentratibnr in' Sediment 1 j.. ,, , from R10. (pCf/kg)
-l
' i.. ' l [ , Radtonuclide' Collection Date~ 6/11/88 .3 l' 'Cs-134 21 (21)*
- 1. '
'. Cs-137 150 (21) ,
J . 1 a
.. Radionuclides Collection Date 11/5/88 - _.
i d 4-2 O t-Cs-134 16 (9.8) Lh 'Cs-137
.' 130 (9.2)
Ll. . t. k -
'f' I - *1.96 s (Due to counting statistics.)
I i i
=
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nn - n.., i s *? 4 d 84 - q ~ 5 II.G. Sample Crosscheck Program
.i .
'. !, 7 To assure the accuracy and precision of the environmental data obtained from the radiation surveillance program provided for the Fort
~
St. Vrain' reactor, Colorado State University participates in a number of interlaboratory and intralaboratory quality assurance programs. The ,
? . U.S. Environmental Protection Agency (EPA) sponsored laboratory l ~ - intercomparison studies program is the principal crosscheck. This
- j. involves the analysis of a variety of environmental' media containing i ._
various levels of radionuclides. The media, type of analysis and frequency of anaYysis for the EPA program are summarized below. I i l Medium - Analysis (radionuclides) , Frequency
?
Water H-3 Triannually l Water Gross beta, gross alpha Bimonthly l Water Co-60, 2n-65, Cs-134, Cs-137 Triannually
- Water I-131 Semiannually
~
Air partic- Cs-137, gross beta, Semiannually ulate filters gross alpha
; /
Milk I-131, Cs-137 Triannually 4 For each radionuclides analysis of a particular medium, three" independent
- l
! measurements are performed and all results are reported to the EPA. It should be noted that' during the year, our laboratory became certified by ,
i the EPA for drinking water analysis. Table II.G.1 gives the EPA crosscheck data for 1988. The EPA uses
)
the term, Estimated Laboratory Precision (ELP), calculated as one standard deviation for one determination. The normalized deviation of I j our mean from the known is calculated as: I l i
'(
~
,X '
. 85' CSU mean value - EPA known value 4- .
Where: a = standard devia_ tion of the mean of all participating laboratory results - '
- n = number of analyse's by our laboratory, normally n=3 -
The control limit is determined by the_ mean range' of all results . and three standard deviations of the range. If any result exceeds two i standard deviations from the mean (warning level), the result is j unacceptable. Whenever our mean value falls outside this limit, the calculations are rechecked and-the sample reanalyzed if possible. During 1988 all results except 12 were within the warning level. The [ results exceeding the warning level have the notation (n) in Table. I I'. G . I . If possible, the corrected values are shown in the table. t The recheck process and conclusion are given below for these samples.-
- 1. No explanation for variation known. All possibilities ,
I investigated. All program samples during this period were
!- reanalyzed and recounted. -
1
-; 2. Count yield in error, new calibration in April produced correct - ] ! value. ; 3. All results in error were low. It is concluded that Co, Ru, )
l Zn, and Cr do not transfer well from the EPA vessel to our l l
- b. ,
laboratory ve.ssel due to chemical form of the tracer q radionuclides. The Cs-137 and Cs-134 results were correct. l All Cs compounds are extremely soluble and therefore , transferred ,w. ell . Therefore, it is concluded that these EPA ] I results do not have any direct bearing on program results for f- any of the radionuclides tested. The efficiency curve for each 1
l l 1 . 9r .. - 86 i detector and each geometry is only a function of gamma-ray- - absorption in the detector. No other conclusion than the'above-is possible. Carrier will be added to future samples.
- 4. Technician allowed excessive decay before ion exchange
[ treatment and subsequent counting. The decay reduced the I-131. concentration below detectable levels. (Technician has since. l been replaced.') - -
~
! 5.. Count yield for K-40 was too high. Calibration was changed on the basis of new calibration result.
- 6. Wrong count yield was used for one of the two Ge(b) detector l
systems. The corrected value was within the EPA warning level.
- Table II.G.2 lists independent results for H-3 in water samples 1
y split.between this laboratory and the Colorado Department of Health, Radiation Control Division and the laboratory at the Fort St. Vrain Generating Station. The comparison between laboratories in general was { acceptable. !
-Table II.G.3 lists the resp 1ts of gross beta analyses of the split i
i water samples. The procedural differences between the laboratories were previously investigated and minimized. It is concluded that the differences can be attributed only to statistical uncertainty. Table II.G.4 shows results of an intralaboratory crosscheck i i. ( program. Replicate samples are independently analyzed., The replicate
! results are not statistically different and imply that the precision o.f the methods is acceptable.
Recently approximately 30% of all laboratory calculations that [ partly involve technician input were recalculated by a different I~ technician. No input or calculation errors were detected. This result l - - _ _ _ . - . . _ , . ,, , - c -. --
.=_ _ _
4 . . l e* 87 gives further credence to the laboratory results which are not solely conputer calculated and listed.
~
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i I
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- - - . - - - - _ _ - _ _ _ _ _ - .________w
. - - . _ _ _ - , - - .--.----r__ - - - _ - - . - - - - - - . , - - - . - - ,- - . , . - . - . , - - - - - . - _ . . - - --. _ , . _ . _ _ _ - -.
g
. - ,A * - - - - . - . - . . . .-. . ]' :.'
ti
- 88 4 .
j ,
' Table II.G.1 EPA Cross-Check Data Summary. - 19 88 y[
I Radio- CSU EPA 1 E.L.P.* Normalized Deviation Date- nuclide Value - Value from known** !
, ~
WATER TRITIUM -
- j. _
3
]
Feb 12 H-3 5400- 3327 362 +10.09 , y
. l .-
Di 1 Jun 10- H-3 430'0 5565 557 -3.99 ; 1 ( Oct 14 H 2300 2316 350 +0.01 WATER, ALPHA / BETA-
.j- -
- Jan 22 alpha 3.7 -4 5 -0.12 beta 7.0 8 5 -0.35,
.; Mar 18 alpha 12 6 5 +2.08 beta 6 13 5 -2.42
~
May 20 alpha 10 11 5 -0.35
# beta 11. 11 5 +0.00 '
l j.
-1.50 F Jul 22 s alpha 11 .15 5 beta 4.3 4 5 +0.12 Sep 23 alpha 4.7 8' - 5 -1.15 beta 7.3 10 -
5 -0.92 Nov 25 alpha 4 9 5 -1.73 beta 8.7 9 5 -0.12 WATER I-131 Apr 8 1-131 7.4 7.5 0.75 -0.38 l Aug 5 I-131 66 76 8 -2.09 Dec 9 I-131 110 115 12 -1.30 EPA Perfortnance Test Oct 18 beta 49 54 5 -1.85 .
-0.23 Cs-134 14 15 5 Cs-137 18 15 5 +1.15
- E.L.P. Expected laboratory precision.
** Normalized deviation = (. CSU mean - EPA known)/( a / n), if this value i t
falls between the upper and lower warning levels, the accuracy is acceptable. t
I
._ . . _ ~ . . . . . ~ . . . . _ . . .
4 89 Table II.G.1 EPA Cross-Check Data Summary. 19 88 Radi o - CSU EPA 1 E.L.P ,
- Normalized Deviation
~.
Date nuclide Value Val ue from known** WATER, GAMMA Feb 5 Co-60 65 69 5- -1.27 Zn-65 78 94 9.40 -2.95 Ru-106 95 105 10.50 -1.70 Cs-134 59 64 5 -1.73 Cs-137 99 94 5 1.56 Jun 3 Co-60 12 15 5 -0.92 Zn-65 91 101 10 -1.73 Ru-1063 135 195 20 -5.20 Cs-134 17 20, 5 -1.15 Cs-137 28 25 5 1.15 Oct 7 Co-603 14 25 5 -3.93 Zn-653 123 151 15 -3.19 Ru-1063 116 152 15 -4.16 Cs-134 . 22 25 5 -1.15 Cs-137 18 15 5 0.92 .
' Cr-513 200 251 25 -3.53 -
MILK , Feb 26 I-1314 <3 4 0.40 ---- Jun 24 I-131 79 94 9 -2.95 Cs-137 54 51 5 0.61 K-405 1540 1600 80 -1.22 Oct 28 I-131 6 106 91 9 2.89 Cs-137 55 50 5 1.85 K-40 1500 1600 80 -2.09 AIR FILTER
~
Mar 25 alpha 18 20 5 -0.69 beta 51 50 5 0.35 Cs-137 16 16 5 0.0 Aug 26 alpha 8.0 10 5 -0.69 beta 29 30 5 -0.35 l Cs-137 13 10 5 1.15 1 i
- E.L.P. Expected laboratory precision.
** Normalized deviation = (CSU mean - EPA known)/(c/n); if this value i falls between the upper and lov.er warning levels, the accuracy is acceptable.
! Tcblo II.G.2 90 Tritium Crosscheck Analyses on Split Water Samples Determined by Colorado State -
University, Colorado Depart:aent of Health, and Public Service Company. Collection Sample Tritium Concentrations pCi/L Date Location CSU CDH PSC : j e
! January A-25* 110,000 (990) 8110 (253) 9240 (541) 1 A 21 <290 -401 (-167) ' <343 E-41 610 (310) 43 (172) 437 (418)
; February, A-25 24000 (560) 21028 (346) 22800 (687)
A-21 600 (350) -5 (-165) <344
; E-41 1400 (320) 1179 (179) 924 (427) i j March A-25 31000 (580) 27400 (727)-
- A-21 780 (290) <344 _.
I E-41 550 (310) <344
! April A 25 4800 (360) 4110 (465-)
j A-21 260 (300) <336 E-41 <250 <339 May A-25 45000 (660) 40300 (829) j A-21 ~~ 470 (310) <334 j E-41 280000 (1500) 246000 (1840) June A-25 33000 (480) 41600 (848) A-21 330 (260) 622 (424) l 38200 (821) E-41 35000 (750) .* ( July s A-25 38000 (770) , 42300 (871) A-21 <260 <367 . E-41 <260 <367 i, , August A 25 4400 (430) 3810 (492) A-21 <250 <365 ' l <365 E-41 <250 . l ,
' September A-25 9000 (500) 9360 (541) ;
A-21 1580 (434) E-41 <250 3400 (461) October A-25 37000 (770) 37500 (B31) E (386) November A-25 23000 (620) 35500 (802) f A-21 550 (310) <346 j E-41 640 (340) ) December A 25 28000 (660) 36800 (820) A-21 960 (320) <356 E-41 740 (340) <348 1 I
- A composite of 1/9 and 1/12 grab sarple.
. l l
L _. . - - _ . _ _ _ _ _ _ - _ - _ _ . _ _ _ - - _ . _ - . - - - - .- . - _ _ _ - - - _ _ - _ - - . . _ _ . - _ . __ .
~ - ,
,'l
- t i , Tcble II.G.3 91 Gross Beta Crosscheck Analyses on Split Water Samples Determined by Colorado State University, Colorado Department of Health, cnd Public Service Ccmpany of l ,!. Colorado. -
l l' I f 1] lj Collection Sample Gross Beta Concentrations pCi/L i Date Location CSU CDH PSC
.I January A-25 15 (6.1) 20 (5) 8.49 (6.56)
A-21 11 (5.8) 9 (4) 10.30 (6.54) l E-41 16 (6.1) 17 (5) 10.50 (6.90)
! February A-25 13 (5.9) 17 (5) 6.72.(5.80) .
A-21 9.9 (5.9) 13 (4) 10.50 (6.04) E-41 11 (5.8) 11 (7) 10.60 (5.99)
~
March A-25 9.4 (5.9) 16.40 (6.77) A 21 5.2 (5.6) 10.20 (5.83) i E 41 32 (7.3) 62.40 (53.50) April- A 25 19 (6.4) 15.60 (6.50) A-21 13 (6.0) 8.00 (5.60) E-41 21 (6.5) 15.70 (7.20) i
<5.13 May A-25 17 (6.3)
A-21 7.1 (5.7) 8.30 (6.40) E-41 12 (5,9) 9.89 (6.52) June A-25 10 (5.8) 6;94 (6.54) l 6.62 (6.42) l' A-21 15 (6.1) E-41 16 (6.2) 11.80 (7.07) July A-25 11 (5.8) 12.10 (6.14) A-21 12 (5.9) 12.00 (6.36) E-41 6.7 (b.6) 9.47 (6.32) August A 25 11 (5.8) 5.63 (6.63)
' A-21 11 (5.9) 6.80 (7.05) .
E-41 . 8.4 (5.6) 8.52 (6.85) September A-25 12 (5.8) 10.10 (6.90) A-21 6.0 (5.6) 14.60 (7.44) E-41 9.1 (5.7) <5.25 i
! October A 25 11 (5.8) 7.12 (6.50)
I A-21 7.0 (5.6) <5.15 E 41 11 (5.8) 8.62 (6.67) l 4 11.00 (7,00) November A 25 35 (12) A 21 11 (5.8) 6.00 (7.00) E 41 9.6 (5.7) --- December A-25 15 (6.0) 11.70 (6.75) A 21 13 (6.0) 13.10 (6.79) E 41 15 (6.0) 13.30 (6.87) L_---._.-_-__. _ _ _ - . . _ _ _ _ _ _ . . . - - _ - -
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II.H. Summary and Conclusions -
/
~
. Table II.H.1 summarizes the radiation and environmental radioactivity measurements conducted during 1988 in the environs of the Fort St. Vrair$. Nuclear Generating Station, owned and operated by Public
~
Service Company of' Colorado. The values for each sample type may be compared to pre-operational and operational periods lor' this reactor, as ' well as to the values from other U.S. environmental monitoring programs (e.g.. EPA 520). 'It must be emphasized, however, that the mean values in Table ~II.H.1 are only the means of the values greater than MDC, the .
' statistically minimum detectable concentrat. 'n. The range also'is'~given only for. detectable measurements. The mean and range v61ues, therefore, are not the true means or ranges if any of the values in the sample population were less than MDC. The format of Table II.H.1 is a requirement of the NRC.
Inspection of Table II.H.1 reveals that there were no individual
- hasurements except I-131 due to release from Denver and/or Boulder hospitals that exceeded the Reporting Level (RL) (see Table III.A.3). .
The Chernoby1 fallout was still observable in several sample types. For the category of gross beta concentrations in drinking water, the mean for the Gilcrest well was again significantly greater than for the reference supply located in Fort Collins. This difference cannot be due to' reactor effluent activity for the following reasons:
- a. None of the individual fission prodyct or a'ctivation product radionuclides measured were significantly higher in the Gilcrest drinking water.
- b. Tritium concentrations measured at Gilcrest were .only slightly i
statistically greater than those in Fort Collins. Assuming
J, ; , l 94 p .: - -
~
that Gilcrest residents consumed only this tap water as their drinking water source, the calculated weighted dose commitment r' ate to the critical individual (adult) was less than 1.2x10~3 mrem / year. This is a negligible dose rate. . Tritium is the only significant radionuclides measured in the air or water effluent from FSV. Since it is far more mobile than any of the specific radionuclides, if in the unlikely event that effluent
.' activity were reaching the Gilcrest aquifer, elevated tritium concentrations would be the first and most sensitive indicator.
'c7 The city of Gilcrest does not filter and treat its water to the _.
same degree as Fort Collins. This has been verified and
- evidenced by the fact that the gamma-ray spectra of the suspended solids from Gil, crest water samples show only elevated concentrations of the natural radionuclides. It has been
~*
concluded in previous reports that the elevated gross beta f concentrations in Gilerest water are due to' elevated . concentrations of the naturally occurring U-238, and Th-232 , 3 decay products. The suspended solids are higher in Gilcrest water samples due to less filtration of the water.
] For the category of tritium in surface water, as has been the case since reactor operation, elevated concentrations were noted at station A-25, the outlet of the (Goosequill) farm pond. A-25 is directly in the a principal effluent route and elevated concentrations should be expected, .! to correlate with release schedules. Elevated concentrations of tritium i
1.
! have never been observed, however, in any human food source in direct or indirect contact with the farm pond water. Downstream surface water I concentrations of tritium have occasionally be.en elevated, but there is r
t
l i significant dilution before any human use of this water. During 1988 elevated tritium concentrations were observed downstream on several occasions but the mean values for the first and second half of 1988 were not significantly greater than in upstream surface water. An historical sumary of tritium concentration 'in upstream, downstream and potable surface water for six month periods from 1974 to 1988 is depicted in Figure II.C.1. The potable water concentrations p1'otted are .those for' the Gilcrest city water well. I-131 was observed again in milk samples from Dairy A-22. Because
- the reactor'did not release any significant fission products during 1988, the source of the I-131 concentrations in milk could not be reactor effluent. It was documented in the 1985 annual report that the j source of the I-131 concentrations during that year was not due to the
~ reactor but due to nuclear medicine use and release upstream of the reactor. This was an important observation as I-131 is certainly a critical radionuclides in numan dose commitment possibilities, a fact of which the general public is aware. This discovery prompted increased .
monitoring for I-131. Upstream nuclear medicine releases of I-131 is, . therefore, the only likely source of the I-131 observed again in milk samples during 1988. Irrigation water samples confirmed this conclusion. Cs-137 was also observed in many environmental samples due to the Chernobyl fallout. j Table II.H.2 presents an additional summary of mean values for selected sample types. The sample types and radionuclides were chosen on the basis of their importance in documenting possible radiation dose i to humans. Air and surface water would be the predominant environmental
.~
e' - 96 transport routes and drinking water and milk would be the predominant sources of radiation dose if signific5nt radioactivity release from FSV occurred. Table II.H.2 also allows comparison to the.three most recent years o.f operation. The arithmetic means in Table II.H.2 were calculated for all sample results. It should be noted that the tabular data presented in the body of this report contain o,nly positive calculated values. Any calculated values less than zero or less than the minimum detectable concentration
. (MDC) are listed as less than the actual MDC for that sample analysis.
~
~'
Howe:ver, the actual result in all cases was used in the calculation for i-
- the arithmetic mean values for the period. Therefore, all values,
~
i negative as well as positive, were included. This procedure is now j generally accepted and gives a proper estimate of the true mean value.
.l Because of this procedure, however, the values listed in Table II.H.2 I cannot be calculated directly from the tabular values in the report. It Inust be emphasized that while it is true that no sample can contain less I than zero radioactivity, due to the random nature of radioactive decay, it is statis'tically possible to obtain sample count rates less than i ! background and hence a negative result. It is equally true that many sample types do in fact have zero concentrations of certain l
l radionuclides. Therefore, to obtain the correct mean value from the distribution of analytical results, all positive results must be i averaged with all negative results. If the negative results were omitted, the resulting arithmetic mean would be falsely biased high. From log-normal analysis of each data set for each 12 month period, j# the geometric mean and geometric standard deviations are also presented in Table II.H.2. The log-normal probability treatment is to plot all
m ---u.. .-.m _ _ ._.. -_L..., - -
- a. $ _ _
- 97- - -
[l;
' data for 'each sample type over: the ~ year on_ log-probit coordinates.- The
~>
. samples are ranked by increasing activity concentration and the cumulative percentage of rankings are plotted on the probit' abcissa
'~
versus the activity concentration of the log ordinate. The geometric p mean value, gi , is determined directly from the 50th percentile point. 0
-The geometric standard deviation' is simply the slope of the line which can be calculated from the ratio between 84~.1. percentile point and the' 50th percentile. In a normal distribution, the arithmetic standard
- deviation is~an additive parameter to the arithmetic mean, i.e. (i+o); -
whereas, in the logNormal dist'ribution the geometric standard
- deviation, o g, .is a multiplicative, parameter to'the geometric mean (i glog). The area betweeng X multiplied by og and Ag divided by o g 1 should contain 68% of the frequency values. With the log-normal analysis, no bias results from using either actual values or less than MDC values in estimating the. geometric mean. The geometric mean is identical to the median. .
4
! From the values _ presented in Tables II.H.1 and II.H.2 and the 1.
tabular data of the report, the following observations and conclusions 1;1 - may be drawn: .
- 1. Tritium was again the only radionuclides that was detected in significant concentrations in any of the effluent pathways that
.( ~
l could be attributed to reactor operation. Since the tritium is L released as tritiated water, the dilution by the surrounding hydrosphere is great. Although in 1988 a few elevated levels of tr'itiated water could be detected in downstream surface water samples, the mean values of downstream surf ace water was not statistically greater than upstream concentrations. The
~
.3 " .-
98~ - N ' tritium concentrations measured in milk produced by the nearest 1, a
- dairy herd were also all less than MDC. ~ ,,
a >
- 2. Figure II.C.1 is a plot'of tritium measured in surface water samples over the period 1974-1988. During the period the i predominant source term is that of fallout deposition. There is .some delay period in the peaks due to the mean residence ;
1 time of tritium in the hydrosphere and input from other areas; q. 1 Beginning in 1981, an increase can be observed in the
' LJ 1 '
downstream locations relative to upstream. This small increase 1- . I _ is statistically significant, however, the radiation dose commitment that can be calculated as a result of possible ingestion of this as drinking water was found to be negligible [ p as compared to natural background radiation dose rates. This
'i- was discussed in the 1986 annual report.
- 3. As in every previous report, it was again apparent that for f ' '
.- most sa'mple types the variability observed around the mean values was great. This variability is due to counting t-statistics and methodological variation, but principally due to
;- true environmental variation (often termed sampling error). It 4
must be recognized and accounted for in analysis of any set of i environmental data before meaningful, conclusions can be drawn. [
- 4. The Chernobyl accident fallout has totally obscured what
[ j- fission product debris has remained in the FSV environs from , I the October 1980 Chinese atmospheric nuclear weapon test. The biosphere will contain the Chernobyl fallout, particularly
]i Cs-137, for an equally long period. Nuclear weapon test fallout has since the inception of the project been noted to be jl
g_. . - -- --. I ,
,,, Jj in (, - .
+'
- p <
M , gg y the predominant source. term above natural background. It is the variation in fallout deposition, in addition to the
- j. variation in naturally occurring radionuclides, that mandates the large number of environmental- samples to detect any possible radioactivity' due to reactor effluents. A simple comparison of pre-operational and operational values is of
~
little value for most sample types' because the fallout E' '
' deposition was considerably greater during the pre-operational period.
- 5. The prompt and sensitive detection of the Chinese weapon test t
and Chernobyl fallout in the past assures that the environmental monitoring program is of adequate scope and sensitivity to detect any accidental releases from the FSV j reactor operation. It can be concluded from the data collected by the environmental monitoring program that the radiation dose commitments calculated for the closest inhabitants or other 1 parts of the nearby ecosystems due to current. reactor effluents are negligible. Natural background radiation and the dose ,j i commitment from atmospheric fallout are the only known significant sources of radiation dose to the residents of the area. i
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. .. 79 . . . .
344 X 131 221 11 00 21 2 m m e H. a a e e I tem tem tc tc tc I nra nra nn nn nn ete 7 ete ee ee 7 ee e usr 3 usr cr 1 cr 3 cr l l nt 1l nt ae 3 ae 1jf 1 ae jf 3f ws - f ws 3jf b - de - de sde a - fop sf op CAR T HEDU CEDU HAR IAR
h , . . 112 - III. Radiological' Environmental' Monitoring Program
' ~
A. Sample Collection and Analysis Schedule .. Table .III.A.1 outlines the sampling design, the collection , frequency and the type of analysis for all environmental samples. - It should be repeated that this schedule was only adopted January 1,1984,
$ and while different in certain aspects from the previous schedule, has as its intent the same objective. That objective is to document the -
radiation and radioactivity levels in the critical pathways of dose to N humans. Such data is necessary to prove that reactor radioactivity -
~
effluents produce environmental concentrations that are within appropriate, environmental protection limits and at the same time are as
,i j low as reasonably achievable.
During 1988, there were no changes in the sampling program. As noted in II.D. A-22 dairy temporarily suspended the supply of milk samples. The control dairy, R-8, went out of business in December and a [ - new location was found starting in January of 1989. Table III.B.1 gives the description of each sampling location by f i i number, sector and distance from the reactor. These descriptions were expanded somewhat in this report. Each of these sampling locations (except certain reference locations) can be identified on scale maps j (Figures III.B.1 and III.B.2). Topographical maps showing greater I i detail, as well as photographs of principal sampling sites are on fil'e in the CSU laboratory. . During June of 1988 the land-use census was conducted to determine the locations of the nearest residence, the nearest milk animal, and the I- nearest garden producing broad leaf vegetation in each of the 16 meteorological sectors around the reactor. These locations by address 4 i
m i' . - --
- 1 1
113
~
f' are shown in Table III.C.1. Figure III.C.1 shows these locations in each sectore At the time of the 1988' census it was verified that the .- closest permanent residence in Sector 16 (17250 CR 19 1/2) was the critical receptor with regards to mean annual dose commitment. 'However, -
. that residence was abandoned early in the fall. The closest resident now is at the Russell farm F-16.
A few residents in the sampling sectors up to a distance of 8 km ' ' from the plant have cows or goats that could be used for personal milk
. consumption. However, from direct discussion with these persons, this is not. a common practice and most milk produced is transported to commercial processors.- The milk produced locally is diluted by a large milk shed, processed and distributed over a large area for consumption.
Table III.A.2 lists the LLD concentration values for each sample
> type and radionuclides measured in this report. These LLD values are the actual values pertinent to the sample sizes, counting yields, and counting times used in the project. Typical decay periods were used in the calculations. It should be noted that the LLD values are in all -
cases equal to or less than those required by the technical
; specifications.
l
. Table III.A.3 lists the USNRC reporting level for each sample type and radionuclides.
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15 18100 CR 19** 8560 CR 38** 19461.CR 17** 16 9239 CR 38** 19108 CR 19** 18986 CR 19** , i 4
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- 131 i . l. 'I Appendix I During 1988 Dr. Gerald M. Ward, Professor of Animal Sciences was hired as a liason between the local farmers and ranchers and this program. Dr. Ward is 1 a dairy scientist but has had over 25 years ct evp3rience in many aspects'of ti
{ fallout studies and of dairy food chain 'trancv-t of fission products,
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, principally, Cs-137. Dr. Ward _was instrumental in many discussions with the i
local farmers and provided the following report. . 1 l e
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- g. 132-Survey of. Dairy Farms Provi. ding Milk for Environmental Monitoring of-the St. Vrain Nuclear Power Plant i
March 24-25, 1988 2 1i' Gerald M. Ward . c All of the farmers were contacted except Arlo Johnston (near Johnson's
.s Corner) although his dairy operation was observed. All operations are rather conventional for Northern Colorado. Cows are kept permanently in open lots on-I a dirt surface. The winter manure pack is removed'at this time of year. Scoe i
of the lots have an open-faced shed for shelter, some have a fence on the 1 .. . north side and some no protection at all. During cold weather and muddy i 4 t spells straw is often placed in the corrals for bedding. The one exception is f a covered feeding area at the Henrickson Dairy which is also the largest i (about 300 cows). However, most of the time is spent in an open shed. ; [ Herd sizes except for Henrickson range from 50 to 90 cows per dairy. I The survey day was very windy and dusty. It is obvious that top soil can ! flow into corrals. The surface area of corrals in northern Colorado is about 350.to 500 ft 2per cow which means that the. potential conta'mination area is a I' smal2. 1 The only drinking water supply for cows in,all cases except one is from a !
.' rural water supply which comes from Carter Lake. On one farm (Percy I
Odenbaugh) cows have access to water from an irrigation ditch during the time 1 that water is running in the ditch. His cc>ws, unlike on other farms, also k have access to water from a well on his farm as well as from the rural water I
.j supply.
None of the milking cows on any of the farms have access to pasture or green-chopped feed. Hay on all the farms is stacked outside and is not l I covered. Silage is stored in trench silos and generally covered with plastic.
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. Two' dairies, Henrickson and Marostica purchase all their hay, the latter-7 fr.om his next-door neighbor. The other farmers produced a part or all their
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own hay. Purchased hay is generally from Weld Co. Those who feed corn silage , l' produce their own. l , No apparent. Differences between dairy farms were noted that could be used 1
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to explain differences in the transfer of airborne radionuclides to. milk. A few goats were seen in a yard near the Odenbaugh farm. , It was not - determined if they were milk goats. 1 i- .. t t
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