United States Eastern Environmental EPA 520/5-84-012
Environmental Protection Radiation Facility June 1984
Agency P. O. Box 3009
Office of Radiation Programs Montgomery, AL 36193
Radiation
Radioactive
tudy at the
Savannah River Plant
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EPA 520/5-84-012
AN AIRBORNE RADIOACTIVE EFFLUENT STUDY
AT THE SAVANNAH RIVER PLANT
July 1984
U.S. Environmental Protection Agency
Office of Radiation Programs
Eastern Environmental Radiation Facility
P.O. Box 3009
Montgomery, Alabama 36193
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STUDY PARTICIPANTS
Eastern Environmental Radiation Facility (EERF), U.S. EPA, Montgomery, AL
R.L. Blanchard* R.J. Lyon
J.A. Broadway* M.O. Semler
R.S. Call is E.L. Sensintaffar*
Three Mile Island Field Station, EERF, Middletown, PA
W.P. Kirk*
U.S. EPA Regional Office. Atlanta. GA
C.L. Wakamo
Georgia Institute of Technology, Atlanta, GA
B. Kahn*
Savannah River Plant, Aiken, SC
G.A. Smithwick R.A. Sigg
D.J. Ratchford R.A. Geiger
D. Ross A.J. Garrett*
* Designates authors.
Acknowledgment
The authors wish to express their appreciation to Mardy Wilkes for
her tireless effort in expeditiously preparing this manuscript.
ii
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FOREWORD
Under the Clean Mr Act, Sections 112 and 122 as amended in 1977, the
Office of Radiation Programs (QRP) of the United States Environmental
Protection Agency is currently developing standards for radionuclides
emitted to the air by several source categories. In order to confirm
source-term measurements and pathway calculations for radiation exposures
to humans offsite, the ORP performs field studies at selected facilities
that emit radionuclides. This report describes the field study conducted
at the Savannah River Plant (SRP), a laboratory operated by E.I. du Pont
de Nemours and Company for the U.S. Department of Energy.
The purpose of the study at SRP was to verify reported airborne
releases and resulting radiation doses from the facility. Measurements of
radionuclide releases for brief periods were compared with measurements
performed by SRP staff on split samples and with annual average releases
reported by SRP for the same facilities. The dispersion model used by SRP
staff to calculate radiation doses offsite was tested by brief
environmental radioactivity measurements performed simultaneously with the
release measurements, and by examining radioactivity levels in
environmental samples.
This report describes in detail all measurements made and data
collected during the field study and presents the results obtained.
Readers of this report are encouraged to submit any comments or
suggestions they might have. Requests for further information are also
invited, and should be addressed to the Environmental Protection Agency,
Office of Radiation Programs, Washington, DC, 20460.
Glen L. Sjoblom, Director
Office of Radiation Programs
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CONTENTS
Page
1. INTRODUCTION 1
1.1 Purpose of Study 1
1.2 Plant Description and Effluent Sources 3
1.3 Off-Site Radiation Exposure and Environmental Monitoring . . 7
1.4 The Study 11
2. AIRBORNE RADIOACTIVE DISCHARGES 14
2.1 The Tritium Production Facility 14
2.1.1 Gaseous Effluent System 14
2.1.2 Source Sampling 15
2.2 The Reactor Facility 15
2.2.1 Gaseous Effluent System 16
2.2.2 Source Sampling 19
2.2.3 Analyses 19
2.2.4 Results and Discussion 20
2.3 The Chemical Separation Facilities 23
2.3.1 Gaseous Effluent System 24
2.3.2 Source Sampling 24
2.3.3 Analyses 26
2.3.4 Results and Discussion 26
3. RADIOACTIVITY IN THE PLUME 28
3.1 The Tritium Production and Special Radionuclide Facility . . 28
3.1.1 Meteorology and Sampling Sites 28
3.1.2 Sample Collections and Measurements 32
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(CONTENTS)-Continued
Page
3.1.3 Analyses 33
3.1.4 Results and Discussion 33
3.2 The Reactor Facility 37
3.2.1 Meteorology and Sampling Sites 37
3.2.2 Sample Collections and Measurements 40
3.2.3 Analyses 41
3.2.4 Results and Discussion 42
3.3 The Chemical Separation Facilities 48
4. ENVIRONMENTAL MONITORING 49
4.1 Sample Collection 49
4.1.1 Vegetation and Soil Samples 49
4.1.2 Food Samples 49
4.2 Analyses 49
4.3 Results and Discussion 51
5. MODELING 60
5.1 Predicted Airborne Concentrations 60
5.1.1 Results from EPA Modeling 60
5.1.2 Results from DOE Modeling 71
5.1.3 Discussion 79
6. SUMMARY AND CONCLUSIONS 80
6.1 General 80
6.2 Source Term Evaluation 81
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(CONTENTS)-Continued
6.3 Plume Model Evaluation 81
6.4 Environmental Contamination 82
7. REFERENCES 84
APPENDIXES
A Release Rate of Radionuclides Based on Weekly Composited
Particulate and Charcoal Samples from the Chemical Separations
and Reactor Facilities
B Use of the Penn State Noble Gas Monitor to Assay Kr-85 and Ar-41
in Air Samples Collected During the EPA Survey of the Savannah
River Plant
C The TRAC Laboratory Plume Monitor
D A Comparison of the Inter!aboratory Analyses
vii
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LIST OF FIGURES
Fi gure Page
1.1 The Savannah River Plant Site 2
3.1 An Example Plot of a 15 Minute Averaged Plume Profile in H-Area.
Sample Site Numbers are Circled. Large Letters and Numbers
Designate Roads 29
3.2 SRP Site Meteorology for the 15 Minute Interval Ending at
2 PM EST on December 14, 1982 30
3.3 The Savannah River Plant Site Showing Sampling Locations.
The Sampling Site Numbers are Circled with Arrows Pointing to
Exact Location. Letters and Bold Type Numbers Designate Roads . . 31
3.4 An Example Plot of a 15 Minute Averaged Plume Profile in P-Area.
Sample Site Numbers are Circled. Large Letters and Numbers
Designate Roads 38
3.5 SRP Site Meteorology for the 15 Minute Interval Ending at
12 PM on December 15, 1982 39
3.6 The Concentration of Ar-41 {—) Plotted with the Average Net
External Exposure (PIC) from the Plume for Each Sample
Collection Period 44
o
3.7 The Concentration of Ar-41 as pCi/m (—) Plotted with the
Average Net Count Rate of the Rear Two Quadrants (counts/minute)
of the TRAC Plume Monitor 46
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I
LIST OF FIGURES-Continued
Fi gure Page
4.1 The Savannah River Plant Site and Surrounding Area. Sampling
Locations are outside Plant Site Boundary and are Designated by
Circled Numbers with Arrows Pointing to Exact Locations. Roads
are Designated by Larger Bold Numbers. Letters Designate Site
Areas 50
5.1 Geometry of the Plume for two Representative Tritium Measurements
from H-Area on December 14, 1982 62
5.2 Schematic Layout of Release from P-Area and the Measurement of
Tritium at Site 7 on December 15, 1982 67
5.3 Schematic Layout of Release from P-Area and the Measurement of
Argon-41 at Site 7 on December 15, 1982 68
5.4 The Variation in Calculated Plume Concentration vs. the Angle
from Center Line Direction for Site 7 on December 15, 1982 .... 70
5.5 A Comparison of the December 14 EPA HTO Measurements at H-Area
with SRL Calculated Concentrations 76
5.6 A Comparison of the December 15 EPA Argon-41 Measurements at
P-Reactor with SRL Calculated Concentrations 77
5.7 A Comparison of the December 15 EPA HTO Measurements at
P-Reactor with SRL Calculated Concentrations 78
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LIST OF FIGURES-Contlnued
Figure Page
B.I The Gross Count Rate of Argon-41 with 2-0 Error Bars. Also
Shown is the Mean Nocturnal Background ( ) with its 2-0
Uncertainty (—) B.7
B.2 The Net Concentration of Argon-41 Corrected for Decay to the
Midpoint of Collection ...... B.8.
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LIST OF TABLES
Table Page
1.1 Atmospheric Radionuclide Releases from the SRP in 1981 4
1.2 Highest Radionuclide Releases to the Atmosphere at the SRP
in 1954-1980 6
1.3 Calculated Radiation Dose Equivalent Commitments Due to
Atmospheric Radionuclide Releases from the SRP in 1981 6
1.4 Summary of Environmental Radiological Monitoring Results
at the SRP in 1981 9
1.5 Locations of Sampling Sites 13
2.1 Airborne Releases in Curies from Reactor Areas in 1981 16
2.2 Stack Effluent Samples from P-Reactor ... 22
2.3 Source Term Comparison - P-Reactor 23
2.4 Airborne Releases in Curies from Separation Areas in 1981 .... 24
2.5 Chemical Separations H-Area Stack Effluent Samples 25
2.6 Chemical Separations F-Area Stack Effluent Samples ........ 27
3.1 Measured Concentrations of HTO and Computed Total Concentrations
of Tritium in the Plume of the Tritium Facility 35
3.2 The High-Volume Particulate Sampling Data and Results 36
xni
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LIST OF TABLES-Continued
Table Page
3.3 The Average Net Exposure Rate in the Plume during Collection
of the Compressed-Air Samples 40
3.4 Measured Concentrations of Ar-41 in the Plume from P-Reactor ... 43
3.5 A Summary of the Mobile Plume Monitoring Data for each
Collection Period with the Corresponding Ar-41 Concentration ... 45
3.6 Measured Concentrations of HTO in the Plume of the Reactor
Facility . 47
4.1 Weights of Environmental and Food Samples Analyzed 52
4.2 The Tritium Concentrations in Vegetation and Food Samples .... 53
4.3 Radionuclide Concentrations Measured in Vegetation and Soil
Samples on Site 55
4.4 Radionuclide Concentrations Measured in Foods Collected near
the Savannah River Plant 58
5.1 Calculated and Measured x/Q Values for Tritium at Site No. 3
on 12/14/82 61
5.2 Calculated and Measured x/Q Values for Tritium at Site No. 4
on 12/14/82 63
5.3 Argon-41 Measurements at Sites 6,7, and 9 on 12/15/82 . . . . . .65
xiv
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LIST OF TABLES-Continued
Table Page
5.4 Calculated and Measured x/Q Values for Tritium at Site No. 6
on 12/15/82 72
5.5 Calculated and Measured x/Q Values for Tritium at Site No. 7
on 12/15/82 ................. 73
5.6 Meteorological Input Data for SRP Calculations ..... 74
5.7 Summary of Measured and Calculated Concentrations ... 75
A.I Radionuclide Airborne Effluent Emissions from Chemical
Separations in F-Area . A.2
A.2 Radionuclide Airborne Effluent Emissions from Chemical
Separations in H-Area A.3
A.3 Radionuclide Airborne Effluent Emissions from the P-Reactor , . A.4
A.4 Radionuclide Airborne Effluent Emissions from the C-Reactor . . A.5
A.5 Radionuclide Airborne Effluent Emissions from the K-Reactor . . A.6
B.I Instrument Settings-Room A131, Building 735A, SRP B.4
B.2 Spectral Regions of Interest Setup in Analyzer ......... B.4
B.3 The Gamma-Ray Analyses of the Compressed Gas Samples for Ar-41 . B.6
C.I Plume Measurements C.2
xv
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LIST OF TABLES-Continued
Table Page
D.I Stack Effluent Samples from P-Reactor D.4
D.2 Chemical Separations F-Area Stack Effluent Samples D.5
D.3 Chemical Separations H-Area Stack Effluent Samples D.6
D.4 Radionuclide Airborne Effluent Emissions from the P-Reactor . . D.7
D.5 Radionuclide Airborne Effluent Emissions from the C-Reactor . . D.8
D.6 Radionuclide Airborne Effluent Emissions from the K-Reactor . . D.9
D.7 Radionuclide Airborne Effluent Emissions from Chemical
Separations in F-Area D.10
D.8 Radionuclide Airborne Effluent Emissions from Chemical
Separations in H-Area D.ll
D.9 The Tritium Concentration in the Water of Vegetation and Food
Samples, pC/ml D.12
D.10 Radionuclide Concentrations Measured in Vegetation and Soil
Samples on Site D.13
D.ll Radionuclide Concentrations Measured in Foods Collected Near
the Savannah River Plant D.16
xvi
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1. INTRODUCTION
1.1 Purpose of Study
Under the Clean Air Act, Section 112, the U.S. Environmental
Protection Agency (EPA) is responsible for establishing national emission
standards for hazardous air pollutants. According to Section 118, Federal
agencies that have jurisdiction over facilities that emit such pollutants
shall comply with these standards. The Administrator of EPA reviewed the
information concerning radioactive pollutants in response to Section 122
of the Act as amended in 1977 (Public Law 95-95) and determined that
radionuclides are hazardous air pollutants (Federal Register 44,
76738-76746, 1979). In Section 103, the Administrator is directed to
conduct research and investigations concerning, among other things, the
causes and extent of air pollution.
The Office of Radiation Programs (ORP) of the EPA is currently
developing standards for radionuclides emitted to air by several source
categories (Federal Register 46, 15076-15091, 1983). For most categories,
proposed standards are in terms of dose equivalents committed to the most
exposed persons in the population. These doses are calculated by ORP on
the basis of annual radionuclide emission values reported by the facility
and calculational models -- notably, AIRDOS-EPA -- for the transfer of
radionuclides from source to humans. The Office of Radiation Programs
also performs field studies at selected facilities that emit radionuclides
to confirm source-term measurements and pathway calculations for radiation
exposures to humans offsite. Described here is the field study at the
Savannah River Plant (SRP).
The purpose of the study at SRP was to verify, where possible,
reported airborne releases and resulting radiation doses from the
facility. Because of the short time available, measurements performed at
selected locations during a single field trip were combined with
comparisons of predictions from meteorological data, inquiries concerning
release points, release rates, and monitoring at SRP. The measurements of
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DATE: 12/14/82 TIME: 1:59:59 PM EST
15 MINUTE-AVERAGED WIND FROM 31.DEG AT 5.1MPH
H AREA
UPPER THREE RUNS
CREEK
\ V.
FOUR MILE v^'
CREEK
V
Fig. 1.1. The Savannah River Plant site
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radionuclide releases for brief periods were compared with measurements
performed by SRP staff on split samples and with annual average releases
reported by SRP for the same facilities. The dispersion model used by SRP
staff to calculate radiation doses offsite was tested by brief
environmental radioactivity measurements performed simultaneously with the
release measurements, and by examining radioactivity levels in
environmental samples collected either as part of this study or as part of
the SRP monitoring program.
1.2 Plant Description and Effluent Sources
The SRP is operated by E.I. du Pont de Nemours and Company for the
U.S. Department of Energy. The plant is located on the Savannah River in
South Carolina, approximately 22 km southeast of Augusta, Georgia. It is
roughly circular in area with an approximate radius of 15 km as shown in
Figure 1.1. Near the center of this area are a number of facilities that
release radionuclides to air and water as a result of normal operations.
Access to these facilities is controlled, and the entire area is fenced
and patrolled, but State Highway 125 passes through the area within 2.5 km
of the nearest facility. However, the highway can be quickly closed at
the site boundaries if warranted by an unplanned release.
The main function of SRP since it began operating in 1953 is
producing tritium and plutonium for the Defense Department. Three
heavy-water-moderated reactors in the 100 Area (see Fig. 1.1), designated
C» P, and K, produce H-3 and Pu-239 by neutron activation of Li-6 and
U-238, respectively. Two additional reactors had been operated, and one
of them is scheduled for further use. A heavy-water (H-2) enrichment
plant (currently not operating) and a plant to purify and recover
contaminated heavy water from the reactors are in the 400 Area.
Three facilities in the 300 Area fabricate fuel and targets for the
reactors. Two chemical separation facilities in the 200 Area, designated
F and H, dissolve irradiated fuel to recover uranium, neptunium, and
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Table 1.1 Atmospheric Radionuclide Releases from the SRP in 1981 (Du82)
Gasef anTJapors Annua1 Release> Cf Source: Area number (Ci)
H-3
C-14
Ar-41
Kr-85
Kr-85m
Kr-87
Kr-88
Xe-133
Xe-135
1-129
1-131
Xe-131m
Particulates
Co-58/60
Sr-89/90
Zr-95
Nb-95
Ru-103
Ru-106
Cs-134
Cs-137
Ce-141
Ce-144
U
Pu-238
Pu-239
Am-241/243
Cin-242/244
Notes: 1) Exponential
2) Amounts of
irradiation
4.0E+5
6.9E+1
6.2E+4
8.4E+5
1.3E+3
8.7E+2
1.5E+3
3.9E+3
2.5E+3
1.6E-1
4.7E-2
6.4E+0
8.9E-5
3.0E-3
1.7E-2
6.4E-2
1.3E-2
7.8E-2
6.4E-4
3.1E-3
3.2E-4
2.7E-2
6.1E-3
4.6E-3
2.8E-3
4.9E-4
1.6E-4
notation; e.g.,
C-14, Kr-85, and
•
3) H-3 releases of l.OE+4 from
100(1. 3E5); 200(2. 7E5);
400(2. OE3); 700(1. 5E1)
100(4. 1E1); 200(2. 8E1)
100
200
100
100
100
100
100
200
100(7. OE -3); 200(3. 7E-2)
200
700
200
200
200
200
200
200
200
200
200
200
200
200
200
200
4.0E+5 reads 4.0xl05.
1-129 are inferred from fuel
the 100 Area and 4.0E+4 from
the 200 Area are estimated to be due to evaporation of
water from
seepage basins.
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plutonium. A major facility for separating, purifying, and packaging H-3
is in the same Area. Research and development are performed in the 700
Area. Radioactive waste is handled and stored at several locations.
Low-level radioactive liquid waste is released to open seepage basins and
eventually outcrops into small creeks and then into the Savannah River.
Gaseous and airborne particulate radionuclides are subjected to various
treatments and then released through stacks (see subsequent sections for
details) at all of the facilities.
The major radioactive emissions in terms of curie (Ci) amounts Kr-85,
H-3, Ar-41, and short-lived fission-produced krypton and xenon
radioisotopes (Table 1.1). In general, the shorter-lived radionuclides
are discharged from reactor stacks in the 100 Area and the longer-lived
radionuclides, from chemical separation plant stacks in the 200 Area.
Tritium and C-14 are released at both locations. Of the H-3 releases
indicated annually for the 100 and 200 Areas, 1.0 x 10* Ci from the
4
former and 4.0 x 10 Ci from the latter were estimated to be due to
evaporation of water at seepage basins.
According to a recently prepared data compilation from 1954 to 1980
(As82), annual radionuclide releases from SRP have been reasonably
constant during the past five years. However, instances of elevated
releases indicate the potential for occasionally higher annual values and
for residual environmental contamination by the longer-lived
radionuclides. Some earlier radioactivity release values have been
reduced over the years by improvements in operations and effluent
treatment. Occasionally, elevated values are due to unplanned events such
as a Pu-238 release in 1969 (See Table 1.2)(Pe79). In 1981, 3.3 x 104
Ci of H-3 in the form of water vapor were released from the tritium
facility in a 2-hour period on March 27 (HP82).
The release values in Table 1.1 and 1.2 are obtained by stack
monitoring that combines continuously recording in-line monitors,
collecting and analyzing gas samples, and continuous collection of
airborne particulate radioactivity on filters with periodic analysis.
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Table 1.2 Highest Radionuclide Releases to the Atmosphere at the SRP
in 1954-1980*
Radionuclide Year Release, Ci
H-3
Ar-41
Sr-89/90
Nb-95
Ru-103/106
1-129
1-131
Xe-133
Cs-137
Ce-144
Pm-147
U
Pu-238
Pu-239
1964
1974
1973
1955
1972
1971
1968
1955-73
1971
1972
1955
1972
1954
1955
1969
1955
1.6E+6
9.0E+5
1.8E+5
4.3E-1
1.3E-1
2.3E-1
2.0E+1
2.1E-1
2.7E+1
3.9E+4
1.4E+0
3.3E-1
1.2E-1
1.9E-1
5.6E-1
2.7E+0
Highest annual releases among values exceeding 0.1 Ci, from As82.
Table 1.3 Calculated Radiation Dose Equivalent Commitments Due to
Atmospheric Radionuclide Releases from the SRP in 1981
Dose equivalent commitment to the total body
Radionuclide MREM (HP82) GASPAR (Ma82) AIRDOS-EPA (EPA79)
Maximum exposed individual at plant boundary, mrem/yr
H-3 0.88 0.74 1.69
C-14 0.066 0.024 0.02
Ar-41 0.18 0.084 0.33
all others* 0.022 0.015 0.23
Total 1.15 0.86 2.27
Population within 80 km, person-rem/yr
H-3
C-14
Ar-41
all others*
Total
100.3
7.5
8.2
1.6
117.6
57.1
0.91
2.8
1.5
62.3
84.6
1.6
6.6
6.9
99.7
* See Table 1.1 for list of radionuclides; contribution by any single
radionuclide to the total is small except, according to AIRDOS-EPA, 1-129
is responsible for about 5 percent of the total dose equivalent to the
maximum individual and over 1 percent of the total collective dose
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Releases of C-14 and Kr-85 are computed by SRP staff on the basis of fuel
Irradiation history and assumption of total discharge. The same procedure
was used for 1-129 until a monitor was installed during 1981, Release
data for some radionuclides are not available for the early years of
operation and some values for early years are calculated from operating
information and later measurements,
•1.3 Off-Site Radiation Exposure and Environmental Momton'ng
The radiation dose equivalent commitments from airborne radionuclides
discharged at SRP during 1981 were 1 to 2 mrem/yr to the total body of a
most exposed person at the plant boundary and 100 person-rem/yt" to all
persons within 80 km of the plant, according to the three calculation!
models cited in Table 1.3. The doses are almost entirely due to external
radiation from 1.83-hr Ar-41 in the plume from reactor stacks, and from
H-3 plus C-14 intake by inhalation and by ingestion of vegetables, milk,,
and meat. Highest organ doses were to thyroid and skin; they were
1.53 and 1.65 mrem/yr, respectively, and 209 and 134 person-rem/yrs
according to the CASPAR code. The elevation of the thyroid dose above the
total body dose is predominantly due to ingesting 1-129, and the higher skin
dose is due to external beta-particle radiation from Ar-41. The calculation
for the most exposed person considers food intake and inhalation by a child,
the most radiosensitive age group.
The dispersion calculations used to compute doses by the MREM program
suggest that H-3 and Kr-85 concentrations in air are detectable at the plant
perimeter, and that all other radionuclides are at very low levels (HP82).
The average values for 1981 are as follows:
H-3 110 pCi/m3
Ar-41 8.1
Kr-85 230
Xe-133 1.1
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Average concentrations for all other radionuclides were below 1 pCi/m ;
those for radioiodine and particles were in the extremely low range of
r 83
10~ to 10~ pCi/m . Concentrations at the perimeter could be
higher by one to two orders of magnitude for downwind periods or occasions
of higher than average releases.
In utilizing these computer codes, SRP staff (for the MREM and GASPAR
codes) and EPA staff (for the AIRDOS-EPA code) made various
simplifications that they consider will not affect the results
significantly. Among the major assumptions were that all airborne
radionuclides are released at a single stack near the center of the plant
area; that radionuclide release is uniform throughout the year; that
dispersion is on the basis of a joint frequency tabulation for
meteorological factors derived for earlier years; that maximum exposure
occurs at the point of highest airborne concentrations at the plant
boundary and that locations of farms that grow the contaminated foods are
uniformly distributed; that persons were exposed throughout the whole year
without shielding and for specified fractions of local food consumption;
and that H-3 and C-14 were in the forms of water and carbon dioxide,
respectively, that entered the exposure pathways as isotopic tracers.
The main evidence of airborne radioactive discharges from SRP found
by the environmental monitoring program routinely performed by its staff
is H-3 in air moisture, rainwater, vegetation, and milk and food. Even at
distances of 25 to 100 km, H-3 levels are still above the analytical
instrument's lower limit of detection of 0.3 pCi/ml. It is possible that
some Pu-238 and Pu-239 concentrations in soil collected at the perimeter
are slightly elevated in comparison to background concentrations. All
other radionuclide concentrations in samples from the plant perimeter are
similar to those taken at greater distances from the plant and to those
found in sampling networks at other sites.
Radiological environmental monitoring samples collected routinely by
the Georgia Environmental Protection Division near SRP in Georgia show the
same pattern of radionuclide levels as the SRP monitoring programs.
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Table 1.4 Summary of Environmental Radiological Monitoring Results at the SRP
in 1981 (HP82)
Radionuclide ranges
Sample
Air moisture
Airborne particles
rainwater
vegetation
milk
food (vegetable,
fruit, grain, meat)
soil
Radionuclide
H-3
Sr-89/90
Pu-238
Pu-239
gamma(Cs-137)
H-3
gamma(Cs-137)
Sr-90
Pu-238
Pu-239
H-3
gamma (Cs-134/137
H-3
1-131
Cs-137
H-3
gamma(Cs-137)
Sr-90
Cs-137
Pu-238
Pu-239
Units
pCi/ml
fCi/m3
aCi/m3
aCi/m3
fCi/m3
pCi/ml
nCi/m2
nCi/m2
pCi/m2
pCi/m2
pCi/ml
pCi/g
pCi/ml
pCi/1
pCi/1
pCi/ml
pCi/g
pCi/g
pCi/g
fCi/g
fCi/g
Plant
29
3
9.6
31
9.7
36
0.32
0.85
22
0.7
4.2
9
13
9
0.10
1.1
0.71
2
16
perimeter
- < 0.3
- < 1
- < 0.4
- < 0.9
- 0
- < 0.3
- < 0.08
0.02
1
8
- < 1
- 0
- < 0.3
- < 1
- < 3
- < 1
- 0.02
- 0.1
- 0.02
- 1
- 10
Di stant
8.5
3
4.7
44
11
5.7
0.33
0.94
8
6
8
7.4
1.2
10
10
-
-
-
0.58
10
(25-100 km)
- < 0.3
- < 1
- < 0.4
- 0.9
- 0
- < 0.3
- < 0.08
- 0.10
- 0.1
- 0.8
- < 1
- 0
- < 0.3
- < 1
- < 3
--
--
--
- 0.54
1
- 9
external radiation
gamma
mR/yr
91
- 55
124
- 55
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Elevated H-3 concentrations, of the order of 1 pCi/ml, were found in air
moisture, rainwater, and milk. Levels of the photon-emitting
radionuclides in these media and in vegetation and soil were similar to
values elsewhere, and were attributed to fallout from nuclear weapon tests
and to naturally occurring radioactivity (EP82).
Special studies are in progress concerning the transport of Kr-85,
1-129, and Pu-238/239 through the environment at SRP. Although Kr-85 and
1-129 are not measured in the routine environmental monitoring program,
these special studies provide information on the migration of specific
radionuclides in the environment. A network of Kr-85 sampling stations
was operated in 1975-6 at distances as great as 140 km from the SRP to
test air dispersion models. Off-site concentrations of Kr-85 as high as
3
420 pCi/m were observed, and even at the distant stations Kr-85 was
detected above the ambient background levels of 14 pCi/m3 (Pe79).
Plutonium studies have shown readily detectable concentrations in 200-Area
soil due to accidental releases in earlier years. The concentration of
plutonium in soil was found to decrease logarithmically with distance,
reaching approximately background values at the plant boundary; in soil
cores to a 15-cm depth, Pu-238. and Pu-239 concentrations were 0.2 - 0.8
fCi/g and 1-9 fCi/g, respectively, outside the perimeter (Mc76). A soil
and a grass sample collected at Jackson, South Carolina near SRP contained
I-129/1-127 atom ratios of 4 x 10"6 and 1 x 10~5 respectively,
compared to background ratios of the order of 1 x 10 (Ba74). The
corresponding 1-129 concentrations in the two samples were 0.6 and 0.9
fCi/g, while background values were near 0.02 fCi/g. Systematic
measurements of 1-129 in soil and vegetation indicate average levels of
2
400 pCi/m near the perimeter, decreasing gradually with distance, but
2
still 6 pCi/m at 150 km. This compares to background levels of 0.2
pCi/m2. At the highest I-129/I-127 atom ratio of 2 x 10~5 near the
plant boundary, the annual dose to the adult thyroid could be 1.6 mrem
(Ka82).
10
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1.4 The Study
The study was undertaken on December 13-15, 1982. On December 13,
SRP staff presented information concerning radionuclide sources, airborne
discharges, effluent air treatment and radionuclide measurements, and
calculations of radiation doses to persons off-site. The EPA staff
presented its study plans. Arrangements were made for collecting samples,
undertaking the field study, and obtaining data concerning releases and
meteorological conditions. Sampling was performed on December 14 and 15.
The component activities of this type of field study are collection
of samples at airborne radioactivity release points, measurement of
radionuclide concentrations in surface air nearby, and collection of
exposure pathway samples such as food, vegetation and soil. Effluent
samples are used to check the magnitude of reported annual releases, to
compare with duplicate sample analyses by plant staff, and to provide the
source term for samples collected simultaneously in ground-level air.
Radionuclide concentrations in surface air are compared with release rates
to test the calculational disperson model. Other environmental samples
are used as radionuclide collectors (integrators) and to compare with
results from the plant environmental monitoring programs.
At the.time of the study, the reactors and the tritium facility were
in routine operation, but the chemical separation facilities were not.
Effluent samples were, therefore, collected from the tritium facility and
one of the reactors (P), and surface air samples were collected 1-5 km
downwind from these facilities, the former on December 14 and the latter
on December 15. The samples of airborne radionuclides included compressed
air, particulate filters, and condensed moisture. External radiation from
the reactor effluent plume was also measured downwind. The SRP staff
provided aliquots of particulate effluent samples collected at one of the
chemical separation facilities stacks during this period, and also one
from several days earlier, when the facility was processing irradiated
11
-------
fuel. Samples of vegetation and soil from the plant site and of
vegetable, beef, and milk off-site were also collected for analysis. The
locations of all sampling sites are listed in Table 1.5.
Some radioactivity measurements were performed on site in mobile
laboratories. Samples were then taken to the EERF laboratory in
Montgomery, AL for radiochemical separations, more sensitive analyses, and
observations of radioactive decay. Measured concentrations of
radionuclides in surface air were compared with concentrations computed
with the AIRDOS-EPA code on the basis of release rates and meteorological
data supplied by the SRP meteorology group.
12
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Table 1.5. Locations of sampling sites
Site 1 - Behind building No. 735A in 700 Area.
Site2 - Intersection of Roads E and F (NW quadrant).
Site 3 - Intersection of Roads 4 and E (NE quadrant).
Site 4 - Intersection of Roads 4 and C (NW quadrant),
Si te 5 - Open.
Site 6 - On Road 7, 460 m (1500 ft) west of intersection with Road F.
Site 7 - On Road 75 400 m (1300 ft) east of intersection with Road F.
Site 8 - At intersection of Roads F and B (NW quadrant).
Site 9 - On Road 6, 610 m (2000 ft) east of intersection with Road F.
Site 10 - "Farming area" on the northeast edge of H Area.
Site 11 - 400 D Area at Monitoring Station (Building 614).
Si te 12 - Seven miles north of Aiken.
Site 13 - In Jackson, South Carolina.
Site 14 - In Langley, South Carolina.
Site 15 - Near the intersection of Highways 19 and 302.
Note--The locations of these sites are shown on maps in Figures 3.4 and 4.4.
13
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2. AIRBORNE RADIOACTIVE DISCHARGES*
2.1 The Tritium Production Facility (H-Area)
The tritium facilities are a complex of buildings in which tritium is
separated from irradiated targets, further purified, and packaged.
Operations are carried out in well-ventilated areas and process cabinets
in which air movement sweeps any unavoidable tritium releases out the
stacks. A large chemical separations plant is also located in H-Area.
This plant processes reactor irradiated enriched uranium to recover
y3j poo
uranium isotopes, " Np and "°Pu. Description of this facility is
included in Section 2.3.
2.1.1 Gaseous Effluent System. The tritium facilities are served by
three 200-ft. stacks and one 75-ft. stack, which normally exhaust a total
of about 279,000 ft3 of air per minute. Tritium in this exhaust air, at
very low concentrations, arises from sources such as exhaust gas streams,
leaks, maintenance work, handling the targets, loading and unloading the
extraction furnace, and packaging operations.
Releases from the tritium process buildings can be categorized
according to the controls that are imposed on the specific streams.
Tritium escapes in very low concentrations in the discard of discrete
batches of inert gas or air, in disposal of the light hydrogen isotopes as
waste from the isotopic separations, and in unavoidable releases into the
general ventilation system (from leaks, opening equipment, etc.).
The first category of release is individual batches of inert gas or
air. Absorption beds are used where feasible to reduce the amount of
tritium that otherwise would be lost this way. One system in use has an
oxidizing bed to convert any elemental tritium into water, followed by a
zeolite bed to absorb the water; another system requires only the zeolite
beds.
* Much of the descriptive material presented in this section was
abstracted from Du82.
14
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A second category of release is from the purification operations in
which tritium ( H) is separated from protium ( H) and deuterium
9
{ H). The final fraction is analyzed for tritium before release and is
recycled if the tritium is recoverable.
2.1.2 Source Sampling. Stack sampling at the tritium production
facility is performed on a continuous basis with Kanne lonization Chambers
and tritium species monitors that measure the tritium concentrations and
determine the ratio of elemental to oxide forms. Composite tritium
release data for the area were provided by SRP personnel for purposes of
comparison with environmental sampling. Total tritium released during the
environmental sampling period (9:00 a.m. to 3:00 p.m., December 14, 1982)
was 154 Ci at 7,130 uCi/sec, composed of 62 percent tritiated water vapor
and 38 percent elemental tritium (Ra82). Extrapolating from this
5
information an annual estimate of approximately 2.25 X 10 Ci/yr of
tritium would be released from this area, which would include
approximately 1.40 X 105 Ci/yr of tritiated water and 0.85 X 105 Ci/yr
of elemental tritium. This total compares closely with reported releases
of 2.7 X 105 Ci for these facilities during 1981 (Du82).
2.2 The Reactor Facility
At the time of this study, there were three operating reactors at the
Savannah River Plant. These were the P, K, and C reactors. The P reactor
was selected for measurements during this study because of its remote
location from other sources. The P reactor is one of five original
reactors at SRP that is uranium fueled with heavy water (D?0) used as a
moderator and coolant. Secondary cooling is provided by once-through
water from the Savannah River. These reactors are production reactors
that are designed specifically to create excess neutrons that can be used
to make specific isotopes. They do not produce steam or electricity.
Power levels for these reactors are variable; however, they typically
operate at around 2,000 megawatts-thermal.
15
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Airborne releases from the reactor facilities are responsible for
nearly one-half the off-site airborne radiation dose. The major
radionuclides contributing to the off-site dose are tritium, carbon-14,
argon-41, and krypton-xenon. Reported releases for 1981 for the three
operating reactors are shown in Table 2.1 (Du82).
Table 2.1 Airborne releases in curies from reactor areas in 1981
Nuclide P Area K Area C Area Total
Tritium
Carbon-14
Argon-41
Krypton-85m
Krypton-87
Krypton-88
Xenon-133
Xenon-135
Iodine-131
Total Alpha
Other Beta-
Gamma
2.5E+4
1.4E+1
2.0E+4
7.0E+2
2.6E+2
4.6E+2
2.4E+3
1.3E+3
3.4E-3
1.1E-6
1.5E-4
5.7E+4
1.3E+1
2.0E+4
3.3E+2
4.3E+2
6.1E+2
1.1E+3
9.1E+2
1.5E-3
3.6E-6
4.2E-4
3.3E+4
1.4E+1
2.3E+4
2.7E+2
1.9E+2
4.1E+2
3.9E+2
3.7E+2
2.1E-3
4.0E-6
3.3E-4
1.15E+5
4. IE +1
6.3E +4
1.3E +3
8.8E +2
1.5E +3
3.9E +3
2.6E +3
7.0E -3
8.7E -6
9.0E -4
2.2.1 Gaseous Effluent System. Radionuclides are released to the
atmosphere as a result of routine operation of P, K, and C Reactors from
three atmospheric release points--
- at the 200-foot-high stack,
- at ground level, from evaporation of disassembly basin water,
- and at ground level from evaporation of water purged from the
disassembly basin to a seepage basin.
16
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Tritium Stack Releases
Tritium, in the form of DTO, is released to the ventilation system
and, therefore, to the stack by evaporation of process water exposed to
air flowing through the process area. During reactor operation, small
amounts of D20 containing DTO are evaporated from slow leaks in pipe
flanges, valves, and from exposed D20 process water. During reactor
shutdown, DTO is evaporated when pipes or valves are opened for inspection
and maintenance work, and when wet fuel, targets, and control rods are
removed from the reactor. Releases of tritium from the stack are
continuously monitored by on-line Kanne Chambers and by collecting
dehumidifier samples daily and analyzing the condensate for tritium.
Tritium Releases from the Disassembly Basin
Although the discharged fuel and target assemblies are rinsed with
water before being placed in the disassembly basin, some tritium is
transferred to the disassembly basin with process water that adheres to
the assemblies. Some water vapor containing DTO evaporates at ground
level from the disassembly basin and from the seepage basin to which the
disassembly basin water is occasionally purged.
Tritium Releases from the Seepage Basin
Disassembly basin water is normally recirculated through filters and
deionizers to clarify the water and to remove radionuclides. Tritium is
not removed in the process. When the tritium content of the disassembly
basin water has built up through several reactor discharges to a
procedural control range of 0.2 to 0.4 microcuries/ml, water is purged to
a seepage basin through filters and deionizers. This controls the
airborne tritium levels in the plant and the consequent exposure to plant
workers. Based on average atmospheric conditions, 30 percent of the
tritium thus purged evaporates from the basin each year.
17
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Releases of Other Radi'onucli'des
Fission product noble gases (isotopes of xenon and krypton) are
released to the reactor coolant from small defects in fuel and target
assemblies and occasionally, but rarely, from failures in the depleted
uranium target assemblies. The gases diffuse to the helium blanket gas
system and, because of leaks in the pressurized gas system, can enter the
process ventilation system, where they are released from the 200-foot
stack. Noble gas releases are continuously monitored using a Ge-Li
detector system and reported hourly by remote readout (Du82).
Argon-41 is produced by neutron irradiation of natural argon in the
air space that exists between the reactor tank wall and the thermal
sideshield. The radioactive argon (1.83-hour half-life) diffuses to the
process area ventilation system and is released from the 200-foot stack.
The confinement system filters, consisting of moisture separators,
particulate filters, and carbon beds do not prevent the release of tritium
and noble gases to the atmosphere.
Carbon-14 is produced in the moderator in three ways: from (n, a)
reactions with naturally occurring 0 in the D^O process water, from
(n, p) reactions with N present as dissolved gas in the moderator or
as nitric acid used to control the moderator pH, and from irradiation of
0 present in the air around the reactor tank wall. Most of the carbon
in the moderator is removed as carbonates by the moderator ion-exchange
purification system. Some of it, as COp, enters the pressurized blanket
gas system and is exhausted through the stack. The calculated total
annual releases of * C from the three reactors operating at SRP for the
three periods, 1978, 1979 and 1980, were 34, 33, and 41 curies,
respectively.
Iodine-131, a fission product, is released to the process room air
by the same pathways as xenon and krypton. The fraction of iodine
released through the carbon filters is 5X10 (Du82). Releases of
particulate radionuclides and 1-131 are continuously monitored using
Gelman (type A-E) filter paper and charcoal filters, respectively.
18
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2.2.2 Source Sampling. Samples of air being released from the stack at
the P-reactor were obtained through the facility's sampling system. This
system included a 1.0 inch line running from the 148 foot level on the
stack to a sampling room where particulate and charcoal filters could be
accessed. Flow through the line was maintained at 1 cfm. Filters are
routinely changed once each week, however, both the particulate and
charcoal filters were obtained on the morning following environmental
sampling (December 16, 1982). The total sampling time for these filters
3
was 3 days and included a volume of 122 m . Stack flow during the study
•j
was 46 nr/s.
Gaseous samples were collected by EPA personnel from the sampling
system on December 15, during the time environmental samples were being
collected. The gaseous samples included two sealed Marinelli beakers,
each having a volume of 1.16 liters. The two beakers were simultaneously
filled by flowing air from the sampling system through the two beakers in
series. Air was allowed to flow through the beakers at a rate of about 1
cfm for five minutes (approximately 120 volumes). The port in the sample
supply system used in collecting these samples was downstream from the
particulate and charcoal filters.
In addition to the Marinelli beakers, two small gas cylinders were
used to contain approximately 20 liters of air from the sample port. A
small compressor was used to collect the samples at a pressure of
approximately 400 psi. A sample of water from the reactor dehumidifier
condenser was also obtained for tritium measurements.
Filter samples including both particulate and charcoal samples from
the exhausts of each of the three operating reactors for the week of
December 6 through 13, 1982, were also obtained. These samples were split
with the SRP Laboratory for comparison of analytical methods and
measurements. Results of the analysis of these samples appear in Appendix
A.
2.2.3 Analyses. The 72-mm fiberglass filters and the charcoal
were analysed for gamma emitting isotopes with a high purity germanium
detector and spectroscopy system located in the EPA mobile laboratory at
19
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SRP. The initial analysis was started approximately 1 hour after the
filters were removed from the reactor. Gaseous samples in the 1.16 liter
Marinelli beakers were also analysed for gamma emitting radionuclides on
site 55 minutes after collection. After the initial analysis, all filter
samples were returned to SRP Laboratory personnel to split the samples for
comparison analysis. Fiberglass particulate filters were cut in half and
charcoal sample portions were weighed to provide both EPA and SRP with
samples. The EPA portions of these filters and the small gas cylinders
were returned to the EPA-EERF laboratory for additional analyses.
Analyses at EERF included gamma spectroscopy on filter and charcoal
samples. The fiberglass filters were then chemically treated to perform
individual analyses for isotopes of uranium, plutonium, americium, and
strontium (Li83). Gaseous samples were tested for Kr-85, using a
cryogenic separation system (St71), and for tritium and C-14 (Go75) .
2.2.4 Results and Discussion. Concentrations and release rates for
the radionuclides found in these samples are listed in Table 2.2.
Analysis of the particulate filters resulted in activities below
detectable limits for all radionuclides except uranium-238. Charcoal
samples were analyzed specifically for iodine-131 and also were below
detectable 1 imits.
Water obtained from the stack dehumidifier system was measured for
tritium content and a concentration of 1.97 _+ 0.07 nCi/ml was measured.
Based on a moisture content of 23 grains per pound (4.25 g/m ) for the
stack effluent and a flow rate of 46 m3/s a release rate of 385 + 14
was calculated. This compares closely with activities of
1.93 nCi/ml (377 nCi/s) measured by SRP or 30 Ci/day (347 uCi/s) based on
Kanne chamber measurements at the reactor (Ra83). Results of measurements
by EPA and SRP for tritium and noble gases are compared in Table 2.3.
Gaseous stack samples from the P-reactor were analyzed for noble
gases and carbon-14. The results of the measurements (Table 2.2) indicate
that the noble gases make up the majority of the radioactive materials
released from the reactor facilities during normal operations. The
20
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failure to detect Xe-133 was probably due to an unusually high analyzer
discriminator setting (> 80 KeV) that was necessary to eliminate excessive
low-energy pulses due to noise in the power source that was later
corrected. Also, the value listed for Kr-88 is based on the counts in the
196 KeV peak. However, the other peak at 835 KeV was much smaller than
anticipated, indicating that the count rate at 196 KeV was only partially
due to the presence of Kr-88. Thus, it is most likely that the Kr-88
release rate is something less than the 25 uCi/s estimated using the count
rate at 196 KeV.
Comparison of the estimated release rates based on these measurements
and the release rates measured with the SRP noble gas monitoring system
are shown in Table 2,3. Although good agreement is noted for the major
radionuclides, there are some significant differences. Some of these
differences may result from comparison of single grab samples of stack
effluent obtained by EPA with average measurements made by the SRP
monitoring system. Also, as indicated above, it is most likely that the
EERF may have estimated a high value for Kr-88.
21
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Table 2.2 Stack Effluent Samples from P-Reactor
Type Sample
Parti culates
Particulates
Participates
Parti culates
Parti culates
Particulates
Parti culates
Particulates
Particulates
Charcoal
Water
Stack gas
Stack gas
Stack gas
Stack gas
Stack gas
Stack gas
Stack gas
Stack gas
Radionuclide
Gamma emitting
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131
H-3
C-14
Ar-41
Kr-85
Kr-85m
Kr-87
Kr-88
Xe-133
Xe-135
Measured
Concentration
uCi/m3
< 8E-8
< 4E-8
< 8E-9
< 3E-9
< 3E-9
(1.1 + 0.3)E-8
< 1E-9
< 1E-9
< 1E-9
< 3E-7
(8.4 +_ 0.3)E+0
(7 +_ 2)E-3
(2.8 +_Q.2)E+l
(1.2 + 0.2)E-5
(2 +_ 1)E-1
(1.4 + 0.9JE-1
(5+2)E-l
Not Measured
(8 +_ 1)E-1
Estimated
Release Rate
uCi/s
< 4E-6
< 2E-6
< 4E-7
< 2E-7
< 2E-7
(5 ±2)1-7
< 6E-8
< 6E-8
< 6E-8
< 1.3E-5
(3.9 +_ O.DE+2
(3.4 + 0.8)E-1
(1.31 + 0.09)E+3
(5 + l)E-4
(9 + 6)E+0
(6.4 +_ 0.4)E+0
(2.5 +_ l.DE+1
(3.9 +_ 0.6)E+1
Notes: 1) Samples were collected during the following periods;
particulates from 0830 on 12/13 to 0830 on 12/16, water from
0830 on 12/15 to 0830 on 12/16, and stack gas at 1400 on 12/15.
2) Particulate filter samples were split between SRP and EPA,
and results shown are estimates based on assumption of equal
portions.
22
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Table.2.3 Source Term Comparison - P-Reactor
Rach'onuclide
H-3 (12.28 y)
Ar-41 (1.827 h}
Kr-85m (4.48 h)
Kr-87 (1.272 hr)
Kr-88 (2,84 h)
Xe-133 (5.24 d)
Xe-135 (9.11 h)
SRP
(Ra83)
377
1053
17.4
6.1
9.0
14.4
29
wCi/s
EERF
385 + 14
1308 +_ 88
8.9 + 5.9
8.6 + 0.4
25 + 11
Not detected
38.7 +_ 5.8
2.3 The Chemical Separation Facilities
The chemical separation facilities consist of two separate facilities
(F and H) that process irradiated fuel and uranium target materials. Each
separation plant is in a large shielded building called a "Canyon" for
?39
processing the highly radioactive materials. In F Area, Pu, Up,
and U are recovered using the Purex solvent extraction process. This
area also contains the main analytical laboratory, the plutonium
metallurgical laboratory, and the plutonium fuel fabrication facility.
037
The H Area is used to extract special radionuclides, including Np
O OjK
and "°Pu, as well as U, from irradiated uranium enriched in its
235 content. H-Area also contains the Tritium Production Facilities
described in Section 2.1, the Receiving Basin for Off site Fuels, and the
Resin Regeneration Facility.
Releases from these separation areas result in somewhat over half the
estimated total SRP off-site radiation dose from radioactive airborne
emissions. The primary radionuclides contributing to the off-site doses
from these facilities are tritium, carbon-14, and the isotopes of Kr and
Xe (Du82). Emissions from the combined separation areas during 1981 are
shown in Table 2.4.
23
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Table 2.4 Airborne Releases in Curies from Separation Areas in 1981
Nuclide Total
Tritium 2.7E+5
Carbon-14 2.8E+1
Krypton-Xenon 8.4E+3
Iodine-129 1.6E-1
Iodine-131 3.7E-2
2.3.1 Gaseous Effluent System
In the chemical separation process, reactor irradiated materials are
dissolved, then chemically treated to separate the various products.
Major products and byproducts include isotopes of plutonium, uranium, and
neptunium. Airborne effluents from each separation process passes through
individual filtration systems prior to flowing into a common sand filter
and release from a 200 foot stack. The stacks are continuously monitored
for particulates, radioiodine, and krypton-85.
Off gases and particulate radioactivity from most other operations
conducted at these facilities pass through HEPA filters, sand filters, or
both before being discharged through facility stacks. Particulate,
radioiodine, noble gases, and tritium releases are monitored at the major
stacks.
2.3.2 Source Sampling. Particulate filters (72-mm fiberglass) and
charcoal filters for the period of December 5 through 12 and for December
14 through 15 were provided by the SRP sampling system. These samples
were intended to be for comparative purposes. Samples of the earlier
period represented conditions of normal operation, while samples of the
latter period were collected during reduced operations. In addition,
samples of air being released by one of the plants during operation were
collected on a later date by SRP personnel and sent to EERF. Results of
the samples obtained for comparison purposes are shown in Appendix A.
24
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Table 2.5 Chemical Separations H-Area Stack Effluent Samples
Measured Estimated
Radionuclide Concentration (pCi/m3) Release Rate (pCi/s)
Zr-95
Nb-95
Ru-103
Ru-106
Cs-134
Cs-137
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131*
Notes: 1) Particulates
1.6 ^0.2
0.98 + 0.09
2.9 + 0.2
31 _+ 1
0.082 +_ 0.005
0.23 +_ 0.05
2.3 ^0.7
< 8.0
< 1.6
0.04 ^0.01
< 0.0065
0.017 +_ 0.006
0.22 +_ 0.03
0.003 + 0.002
< 0.0025
< 0.15
were collected during
230 +_ 20
140 + 10
410 +_ 20
4400 +_ 180
11 1 7
32 +_ 7
330 +_ 100
< 1100
< 220
6 +_ 2
< 0.91
2.4 _+ 0.8
31 ^ 4
0.4 _+ 0.3
< 0.34
< 21
the period 0900 on 12/14 to
0900 on 12/15 and iodine was collected during the period 0900
on 12/7 to 0900 on 12/14.
2) Particulate filter samples were split between SRP and EPA, and
results shown are estimates based on assumption of equal
portions.
* Charcoal filter sample. All other samples are particulate
filters.
25
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Environmental samples were not collected around these facilities
during the study because the facilities were not processing irradiated
fuel at that time.
2.3.3 Analyses. Particulate and charcoal filters were split by SRP
laboratory personnel and a portion of each provided for comparative
measurements. These samples were analysed for gamma emitting
radionuclides with a high purity germanium detector and spectroscopy
system at the EERF. Fiberglass particulate filters were chemically
prepared and analyzed for the actinides and strontium (Li83). Gaseous
samples were analyzed for krypton-85 with a cryogenic separation process
(St71).
2.3.4 Results and Discussion. Lists of the radionuclides found in
the samples from the H and F chemical separation plants are shown in
Tables 2.5 and 2.6, respectively. The radionuclides found include several
fission products in addition to isotopes of plutonium and uranium.
Although no Np-237 was detected in these samples, any present would have
followed the plutonium separation and been partially obscured in the
spectral analyses by the Pu-242 tracer peak. No specific analyses for
Np-237 were attempted.
Neither plant was operating at normal capacity during the time these
samples were collected so these concentrations and release rates are not
indicative of either normal or maximum values. The sample volume for the
H-facility was 61.2 m3 and 122.3 m3 for the F-facility. The stack
flow rate at both facilities was assumed to be 140 m /s.
The gaseous samples collected by SRP personnel and sent to EPA for
Kr-85 analysis were found to contain an average concentration of
85.8 nCi/m , which would correspond to a release rate of 12.0 mCi/s from
either plant. If this rate were maintained continuously, an estimated
5
total of approximately 7.6 x 10 curies of krypton-85 would be released
per year from the two chemical separation facilities.
26
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Table 2.6 Chemical SeparationsF-Area Stack Effluent Samples
Measured
Estimated
Radionuclide Concentration (pCi/m ) Release Rate (pCi/s)
Zr-95
Hb-95
Ru-106
1-131
Cs-137
Ru-103
Ce-141
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131*
*otes: 1) Participate
1.04 +_ 0.06
1.24 +_ 0.04
1.5 ^0.2
0.02 + 0.01
0.06 +_ 0.02
0.52 +_ 0.04
0.03 _+ 0.02
0.58 +_ 0.08
< 2.0
< 0.4
0.11 +_ 0.03
< 0.033
1.2 +_ 0.2
0.010+ 0.009
0.02 +_ 0.01
< 0.001
0.07 + 0.01
samples were split
144 +_ 9
174 +_ 5
204 _* 28
3^2
9^3
74+4
4^3
80 +_ 10
< 280
< 56
15 1 4
< 4.6
170 +_ 20
1.4 _+1.3
2 +_ 1
< 0.017
10 ^ 2
between SRP and EPA, and results
shown are estimates based on assumption of equal portions.
2) Particulates were collected during the period 0900 on 12/14 to
0900 on 12/15 and iodine was collected during the period 0900
on 12/7 to 0900 on 12/14.
* Charcoal filter sample. All other samples are particulate
filters.
27
-------
3. RADIOACTIVITY IN THE PLUME
3.1 The Tritium Production and Special Radionuclide Facility (Area H)
3.1.1 Meteorology and Sampling Sites. The plume from the stacks of
the tritium facility was sampled at near ground level from 0945 to 1439 on
December 14, 1982. During this period, the wind dispersion data were
continuously recorded by the meteorological station located at H-Area as
well as at six other points on the Savannah River Plant (SRP).
Ventilation wind profile data were also available at seven heights from a
television station antenna to the northwest of the SRP. All dispersion
estimates made for releases from H-Area were based on a compilation of 15
minute averages of wind characteristics as obtained from the local H-Area
station. These summaries included data on average wind azimuth,
vector-averaged wind speed (and speed of maximum wind gust), standard
deviation of wind direction measured in the horizontal plane (a) and
y
standard deviation of wind direction measured in the vertical plane
(CTJ). An example plot of plume trajectory for the 15 minute interval
ending at 1400 is given as Figure 3.1 with the corresponding table of all
simultaneously recorded meteorological data shown as Figure 3.2. Wind
stability class was assigned for each 15 minute measurement interval using
the method developed by Markee (Ma63), which is based on a correlation
between a and the atmospheric stability. Standard deviations in
crosswind plume concentrations a and vertical plume correlations a
were then obtained for each measurement interval using the stability class
obtained above and tables of a and az given by Turner (Tu70). Using
these data, estimates of ground level plume concentrations were made for
each 15 minute interval during each period of sampling.
Two sampling sites for tritium, Nos. 3 and 4, were picked downwind of
the 200-foot stacks in H-Area where ground-level concentrations would be
near maximum values (see Fig. 3.3). Sampling site 3 was located at a
bearing of 220° and less than a kilometer from the tritium stacks (0.93 km)
28
-------
DATE; 12/14/82 TIME; 1:59:59 PM EST
15 MINUTE-AVERAGED WIND FROM 31.DEG AT 5.1 MPH
H AREA
UPPER THREE RUNS
CREEK
-LINE
RR
h-M
V^K'NERO;
FOUR MILE
CREEK
Fig. 3.1. An example plot of a 15-mlnute averaged plume profile in H-Area.
Sample site numbers are circled. Large letters and numbers designate roads.
29
-------
14.9 MIM ENDING: 18:59:59 Z 12/14/82 1:59:59 PM EST 12/14/82
8
504.
522.
AVE —
SPACE AVE. MEAN
(SAM)
AREA AZM SPD/GST(MPH)
0. ? 0.0
HT AZM SPDXGST(MPH)
999F
800F
600F
450F
300F
120F
59F
7F
68.
66.
56.
46.
0.
24.
26.
5.2
4.1
4.1
4.8
0.0?
2.9
3.4
9.3
7.7
8.3
8.5
0.0?
7.0
7.2
SIGA
14.1
16.6
31.6
16.4
25.8
30.3
34.9
SIGE
14.4
16.9
21.3
19.5
4.0
0.0?
22.3
TEMP F
45.53
45.78
47.97
32.00?
50.54
50.94
52.43
56.51
C
D1
D2
F
H
K
P
TV
SAM
AGS
22.
336.
43.
97.
31.
41.
40.
24.
42.
260.
4.5
2.2
2.5
4.5
5.1
3.5
4.8
2.9
4.0
1.8
0.8
9.4
8.5
7.2
9.1
11.6
10.1
9.4
9.3
11.6
49.07
SIGA
0.0?
21.4
50.8
72.9
18.6
30.5
39.6
17.7
27.6
25.9
30.0
SIGE
0.0
11.4
14.3
20.6
11.6
23.2
14.6
17.1
2.4
14.4
ST:2)
Fig. 3.2. SRP site meteorology for the 15-minute interval ending at 2 PM ESJ on December 14, 1982
-------
N
Fig. 3.3. The Savannah River Plant Site showing sampling locations. The sampling site
numbers are circled with arrows pointing to exact location. Letters and bold type numbers
designate roads.
31
-------
This was the nearest collection site. A more distant sampling site (No.
4) was selected at a bearing of 209° and 2.6 km from the stacks where the
plume would be broader and, thus, provide a higher probability of sampling
continuously in the plume. In addition, sites 1 and 2 were selected to
provide background samples: Site 1 was a distant background site
(~ 11 km), while site 2 was at a bearing of 100° and near the facility
(only 2.48 km distant), but, due to the wind direction, was never in the
plume during the sampling period.
3.1.2 Sample Collections and Measurements. Water vapor was
condensed from the atmosphere at each site by pulling air through first a
filter to remove particulates and then a cold trap submerged in a
dry-ice/alcohol bath. Air flow was generally between 10 to 12 liters per
minute resulting in collecting the water from a total volume of about
2,100 liters (2.1 m ). The removal and collection of the water vapor
from the air was assumed quantitative, because the amount of water
collected was consistent with the relative humidity of the air and no
water was ever collected in backup traps when used during earlier tests.
At the conclusion of the sampling period, the frozen vapor in the trap was
allowed to melt and the resultant water transferred to a scintillation
counting vial for later measurement of the tritium that existed as HTO.
During the sampling period, the average temperature and relative humidity
were reported by the Meteorology Section to be 11°C and 50 percent,
respectively.
To determine the gaseous tritium (HT) concentration of the plume, air
samples were collected by opening 1-liter evacuated gas bottles to the
atmosphere and then sealing for later laboratory analysis. Samples of
this type were collected at 0910 at site 1, at 1200 and 1410 at site 3,
and at 1200, 1230, and 1330 at site 4.
While collecting the air and water vapor samples for tritium, a Kurz
high-volume particulate sampler was operated at site 4 between 1114 and
1400. The average air flow, measured with a calibrated minihelic gauge
o
was 50.0 cfm (1.42 m /min.). During this sampling period (166.6 min.),
particulates were collected on a 4-in. MSA dust filter from a total volume
32
-------
3
of 236 m . A similar sampler was operated continuously at site 11 (see
Fig. 3.3) from 1255 on December 14 to 1136 on December 16 (2799 minutes).
"his was considered the background particulate sample. A total volume of
3 3
3171 m was sampled at a rate of 40 cfm (1.13 m /min.).
External gamma-ray measurements were made one meter aboveground at
each site using a Ludlum Model 12S Micro R Meter. Exposure rates measured
were as follows:
Site 1 = 4 uR/hr Site 4 = 6 uR/hr
Site 2=5 uR/hr Site 11 = 4
Site 3 = 10
The increased gamma-ray exposure rate due to the presence of the plume was
easily detected at the close site (No. 3). The other measurements were
near the background exposure rate of about 5
3.1.3 Analyses. The condensed water vapor samples were analyzed
directly for tritium by liquid scintillation counting. The gas samples
were passed through a system that catalytically oxidized the HT to HTO
(G075). The HTO was then collected in a freeze trap and analyzed by
liquid scintillation counting.
The MSA air filters were analyzed by Ge(Li) detector systems to
measure the concentration of gamma-ray emitters. The filters were then
solubilized and analyzed for Sr-90 and isotopes of U, Pu, Am, and Cm. The
analytical procedures used are described in the Laboratory's Radiochemical
Procedures Manual (Li83), and the analyses adhered to rigid quality
assurance procedures (Ea82).
3.1.4 Resul ts and Pi scussion. The concentrations of tritium, in the
form of HTO, measured in the water vapor collected from the atmosphere are
listed in Table 3.1. The tritium was measured as pCi/ml of water.
Tritium in the elemental form was not detected in any of the 1.0 liter
grab samples collected in the evacuated gas bottles at sites 3 or 4. This
3
was probably a result of the high minimum detectable level, 2000 pCi/m ,
33
-------
and possibly not being directly in the plume center line at the instant of
sample collection. SRP reported that 38 percent of the total tritium
discharged was in the form of HT (Ra82).
The average water content of the air during the collection period was
reported by the Plant's Meteorology Section to be 4.9 g/m3. Thus,
multiplying the concentrations in the water by the amount of water
3
per m of air gives the airborne concentrations of HTO shown in the
fifth column of Table 3.1. The total tritium concentrations that are
listed in the last column of Table 3.1 were based upon the measured HTO
concentrations and the percentage of the total tritium discharged that was
of the oxide form.
3
The small amount of tritium, 150 pCi/m , that was measured in the
air at the distant background site (No. 1) was from a source other than
the tritium facility (200-H). Tritium was undetectable in the air at the
nearby background site (No. 2), which strongly indicates that all tritium
measured in the air at sites No. 3 and No. 4 was due to releases from the
Tritium Facility. As expected, the concentration in the air at the near
site (no. 3) was greater (about 3.5 times) than the concentration at the
more distant site (No. 4). This difference is not directly related to
plume concentration, because it fails to account for the variation in
plume direction and the fraction of the time the samplers were out of the
plume. Because of plume dispersion with distance, the sampler at site 4
was probably in the plume a greater percent of the time, but saw a lower
tritium concentration. These results will be compared in Section 5 to
computed concentrations using AIRDOS-EPA with on-site wind dispersion data.
The concentration of radioactive particulates in the plume that were
collected at site 4 in sample SRPP01 are listed in Table 3.2. The only
gamma-ray emitting radionuclides measured were traces of Cs-137. The
concentration of Be-7, a cosmogenetically produced radionuclide, was near
reported background levels (NCRP75), and the background concentrations
measured in samples SRPP02 and SRPP04. No uranium (< 0.3 fCi/m) nor
Sr-89 (< 50 fCi/m ) were detected, but a trace of plutonium may have
been present in the plume. This is not surprising since plutonium is
processed in the H-Area.
34
-------
Table 3.1 Measured concentrations of HTO and computed total concentrations of tritium in the plume
Site
1
2
3
4
Time of
Collection
0945-1439
1035-1420
1100-1410
1120-1330
Tritium
pCi/ml g
30.4
< 12
2,500
700
measured
H20/m3
4.9
4.9
4.9
4.9
as HTO
pCi/m3
150 +_ 45
< 60
12,250 +_ 2,400
3,430 +_ 690
Total
Tritium, pCi/m3
242 ^ 53
< 100
19,760 + 2,800
5,530 + 810
Notes: 1) Discharge rate during sampling = 1.54 X108 uCi/2.16 X104 sec. = 7.13 X 103 uCi/sec.
2) Chemical form - 62 percent HTO and 38 percent HT.
3} Collections made 12/14/82.
4) Site Mos. 1 and 2 are background.
-------
Table 3.2 The high-volume participate sampling data and results
OJ
cr>
Parameter
Site
Date of Collection
Time of Collection
Elapsed time, min
Avg. flow rate, cfm
Total volume, m3
Be-7, fCi/m3(a)
Co-60, fCi/m3
Sr-90, fCi/m3(b)
Cs-137, fCi/m3
U-234/238, fCi/m3
Pu-238, fCi/m3
Pu-239, fCi/m3
SRPP01
4
12/14/82
1115-1400
167
50.0
236
180 +_ 60
< 20
< 15
30 + 15
< 0.3
0.15 + 0.09
0.15 ^0.08
SRPP02
11
12/14-16/82
1255-1136
2799
40.0
3171
110 + 20
< 3
< 2
< 3
0.025 +_ 0.010
< 0.005
< 0.005
Samp! e
SRPP03
6
12/15/82
1010-1337
206
47.8
279
< 210
< 20
< 13
< 20
< 0.3
< 0.08
< 0.08
SRPP04
8
12/15/82
1108-1410
182
38.6
199
140 +_ 70
< 25
< 18
< 25
< 0.3
< 0.08
< 0.08
SRPP05
7
12/15/82
1125-1350
144
41.5
169
< 300
< 30
< 20
< 30
< 0.3
< 0.07
< 0.07
Decay corrected to time of collection.
Unusually high minimum detectable levels of Sr-90 are due to analyzing only
a portion of the filters.
-------
3.2 The Reactor Facility
3.2.1 Meteorology and Sampling Sites. The plume from the 60 meter
reactor stack was sampled at near ground level from 1015 to 1424 on
December 15, 1982, in a similar fashion to that described previously in
Section 3.1.1. Data from the P-Area meteorological station was used to
estimate real-time plume dispersion characteristics of the reactor plant
releases. Standard deviations of plume crosswind (o ) and vertical
(a ) concentrations were obtained identically as described previously.
During this period, the meteorology was continuously monitored and the
predicted position of the plume was reported regularly at 15-minute
intervals.
In addition to the real-time meteorological data, computer-generated
plots of plume trajectory were also prepared by the Meteorological Section
of SRL and kindly provided to the authors. An example plot for the 15
minute interval ending at 1200 is shown as Figure 3.4, together with the
associated table of wind profiles given in Figure 3.5 for all measurements
taken at SRP during the same 15 minute interval.
The Savannah River Plant's Tracking Radiological Atmospheric
Contaminants (TRAC) vehicle was used to assist in locating the plume and
monitor its movement during periods of sample collection. The mobile unit
has 12 NaI{Tl) detectors mounted on the roof that are positioned skyward.
The position of the plume relative to the mobile van can be determined by
the count rates of the four detectors.
Collections of HTO vapor were made at site No. 6: 1.904 km bearing
291° from the release point and site No. 7: 2.209 km bearing 323° from
the release point. In addition, compressed air samples were collected for
Ar-41 and Kr-85 analyses at these sites and at site No. 9: 4.495 km
bearing 328° from the release. Compressed air samples were also collected
at site No. 8: 2.85 km and bearing 120° from the release. During the
entire measurement interval, site No. 8 was upwind of the plume and
therefore provided a station to represent background concentrations. See
Figures 3.3 and 3.4 for the exact locations of these sites.
37
-------
DATE: 12/15/82 TIME: 11:59:58 AM EST
15 MINUTE-AVERAGED WIND FROM 121. DEG AT 11.0MPH
PAREA
PAR
POND
MEYERS
BRANCH
SBCL RR
Fig. 3.4. An example plot of a 15-minute averaged plume profile in P-Area.
Sample site numbers are circled. Large letters and numbers designate roads.
38
-------
513.
149 MIN ENDING: 16:59:58 Z 12/15/82 (11:59:58 AM EST 12/15/82}
531.
co
CO
K
\
\
AVE —
J I
SPACE AVE. MEAN
(SAM)
HT AZM SPD/GST(MPH)
999F
8QOF
600F
450F
300F
120F
59F
7F
149.
151.
150.
150.
0.
147.
148.
20.4 31.2
15.6 27.1
13.3 21.9
12.4 22.1
0.0? 0.0?
7.3 17.1
5.6 12.5
SIGA
8.8
10.9
12.6
13.0
14.8
22.6
27.5
SIGE
8.0
10.6
12.2
11.0
14.7
0.0?
17.8
AREA
TEMP F
56.91
56.93
57.44
32.00?
57.62
61.18
62.23
64.16
A
C
D1
D2
F
H
K
P
TV
SAM
AGS
AZM
1.
133.
23.
131.
158.
137.
136.
121.
147.
137.
150.
SPD/GST(MPH)
? 0.9
12.6
3.3
9.5
12.2
12.3
10.7
11,0
7.3
10.8
3.0
2.5
24.6
11.5
14.1
18.5
23.5
16.3
20.2
31.2
31.2
56.07
SIGA
3.4?
13.5
21.4
12.0
11.5
12.7
10.7
13.4
18.0
12.9
49.0
SIGE
0.3
12.3
15.9
9.1
9.0
11.0
9.8
10.7
8.6
10.8
ST:4)
Fig. 3.5. SRP site meteorology for the 15-minute interval ending at 12 PM on December 15, 1982
-------
3.2.2 Sample Collections and Measurements. Air samples were
collected from the plume at the locations discussed in Section 3.2.1 using
the high pressure gas collection system described in Appendix B (Je80). A
background sample was also collected at Site No. 8. Samples were
transported immediately after collection to the 700 Area and analyzed as
quickly as possible in order to prevent excessive decay of the 1.827 hour
Ar-41 (Ko81). The plume samples were collected in series and as often as
time permitted.
A Model RSS111 Reuter Stokes, pressurized ionization chamber (PIC)
was operated 1-meter aboveground near the compressor throughout the period
the high pressure gas samples were being collected. The average net
exposure rate (5 nR/hr natural background subtracted) during each of the
seven collection periods are listed in Table 3.3. According to the PIC
integrator, the average exposure rate during plume sampling exceeded
background by 6 nR/hr.
Table 3.3 The average net exposure rate in the plume during collection
of the compressed-air samples
Collection
site
6
7
7
7
7
7
9
8
Collection
Start
1015
1048
1113
1142
1203
1230
1321
1108
time
Stop
1040
1107
1133
1200
1227
1248
1340
1410
Average
exposure rate,
6.0
4.4
8.8
6.7
6.2
5.0
4.2
0
net
nR/hr
Notes: 1) Measurements made on 12/15/82.
2) A background exposure rate of 5 uR/hr was subtracted from
each PIC measured gross exposure rate.
3) Collection Site No. 8 was the background site.
40
-------
Water vapor was condensed from the atmosphere at Sites 6 and 7 by
pulling air through first a filter to remove particulates and then a cold
trap submerged in a dry-ice/alcohol bath. Air flow through the systems
v/as initially about 9 liters/minute, but, due to high humidity, the flow
decreased significantly during sampling as large amounts of ice formed in
the traps. At the conclusion of the sampling period, the frozen vapor in
the traps was allowed to melt and the resultant water transferred to
scintillation counting vials for later measurement of the tritium that
existed as HTO. During the sampling period, the average temperature and
relative humidity were reported by the Meteorology Section to be 18°C and
65 percent, respectively.
To determine the gaseous tritium (HT) concentrations of the plume,
air samples were collected by opening 1-liter evacuated gas bottles to the
atmosphere and then sealing for laboratory analysis. Samples of this type
were collected at 1100 and 1130 at Site 7, and at 1410 at Site 8, the
background site.
Kurz high-volume particulate samplers were operated in the plume at
Sites 6 and 7 and at Site 8, the background site. The particulate
collection data are shown in Table 3.2. The average air flows were
measured with a calibrated minihelic gauge. The particulates were
collected on a 4-in. diameter MSA dust filter. The collection data for
the long-term background sample from Site 11 is included in Table 3.2.
^'^*^ Analyses. The airborne concentrations of Ar-41 were measured
vrfth the specialized detector-spectrometer system described in Appendix B
(Je80). Samples were analyzed for 30 minutes, and the concentrations of
Ar-41 measured were corrected for radioactive decay to the mid-time of the
sample collection period. The sample chamber was flushed with P-10 gas
between each analysis.
Five hundred liters to a cubic meter of the gas collected in scuba
bottles were transferred to the laboratory for Kr-85 analyses. The Kr-85
was separated from other gases by a cryogenic technique and transferred to
scintillation vials containing a liquid scintillator (St71). The Kr-85
was then measured by liquid scintillation counting.
41
-------
The condensed water vapor samples were analyzed directly for tritium
by liquid scintillation counting. The gas samples were passed through a
system that catalytically oxidized the HT to HTO (Go75). The HTO was then
collected in a freeze trap and analyzed by liquid scintillation counting.
The MSA air filters were analyzed by Ge(Li) detector systems to
measure the concentration of gamma-ray emitters. The filters were then
solubilized and analyzed for Sr-90 and isotopes of U, Pu, Am, and Cm. The
analytical procedures used are described in the EERF's Radiochemistry
Procedures Manual (Li83), and the analyses adhered to rigid quality
assurance procedures (Ea82).
3.2.4 Results and Discussion. The concentrations of Ar-41 that were
measured in the air collected in the plume from the reactor stack are
listed in Table 3.4. The concentrations varied from less than 600
3 3
pCi/m to over 2,000 pCi/m . This variation was due to movement of
the plume with respect to the collection apparatus during sampling.
During the first sampling period, 1015-1040, the plume was slowly moving
to a more northernly direction. During the next 5 collection periods,
1048-1248, the plume slowly drifted back and forth over the stationary
collection apparatus at site 7. The lower Ar-41 concentration measured at
site 9 was due to an increased distance from the source and directional
variation of the plume during sampling.
The average net pressurized ionization chamber (PIC) measurements
listed in Table 3.3 are compared in Figure 3.6 to the Ar-41 concentrations
measured in the plume during the same time periods. The Ar-41
concentrations and exposure rates followed the same general trends. A
close relationship between the two independent measurements was not
expected, because the PIC measurements respond to other radioactive
components of the plume in addition to Ar-41. But the PIC did detect the
presence of the plume and measured the external radiation exposure
resulting from the plume's presence at that particular location.
42
-------
Table 3.4 Measured concentrations of Ar-41 in the plume from P-reactor
Collection
Site
6
7
7
7
7
7
8
9
Collection
Start
1015
1048
1113
1142
1203
1230
1404
1321
period
Stop
1040
1107
1133
1200
1227
1248
1424
1340
Ar-41,
pCi/m3
1660 + 500
270 + 380
2340 + 750
1810 +_ 740
440 + 630
430 +_ 700
£ 640
300 +_ 650
Notes: 1) Samples collected on 12/15/82.
2) Concentrations of Ar-41 corrected for decay to the midpoint
ofcollection period.
3) The +_ values given are 2-sigma counting errors.
4) See Appendix B for detailed sample collection and counting data.
The Ar-41 plume measurements are compared in Figure 3.7 to the TRAC
Plume Monitor counts for each sampling period. The data used to make this
comparison are given in Appendix C and summarized in Table 3.5. The 60 second
counts from the two rear quadrants of the Monitor, Sectors III and IV, were
averaged for each sampling period. The average net count rates (average cpm
less background), for each period are listed in the third column of Table
3.5. The data from the rear quadrants were used in the comparison because the
compressor was operated about 25 m to the rear of the TRAC Mobile Laboratory.
The similar shape of the two curves in Figure 3.7 shows that a
correlation exists between the counts recorded by the plume monitor and the
measured Ar-41 concentrations. Statistically significant Ar-41 concentrations
were measured for periods III and IV, whereas, the concentrations measured
43
-------
2,400-
2,000 -
E
O
a. 1,600 -
r>
T"
"7
^
"o
.2 1,200 -
1
c
0)
o
c
o
onn
800-
400-
o
1 1
1
1
I
1 1
i
I
1
1
1
L- 1
LMMM^B
1
1
1
1
1
1
-16
>
o
S
(0
(D
m
-12 5.
(0
3
9L
3D
a>
a
-9 I
o
3
m
X
•o
0
(0
C
-6 ®
c
3D
-3
10:00
11:00
12:00
1:00
2:00
Time (a.m. - p.m.)
Fig. 3.6. The concentration of argon-41 ( — ) plotted with the
average net external exposure (PIC) from the plume for each sample
collection period.
44
-------
during periods II, V, VI, and VII were not statistically significant because
too long of decay periods were permitted between sample collections and
analyses (see Appendix B). Concentrations of Ar-41 for these periods were
estimated by using the average Ar-41 (pCi/m ) to CPM ratio for the periods
III and IV, computed to be 0.72. Multiplying this ratio by the average cpm
value for the period yields the estimated Ar-41 concentrations listed in the
last column of Table 3.5. These results will be further discussed in Section
5.
Table 3.5 A summary of the Mobile Plume Monitoring data for each
collection period with the corresponding Ar-41 concentration(a)
Sampling
Period
Collection
Time
tion TRAC System Ar-41,(f) Estimated
(b> Net Counts (CPM)(C) pCi/m3 Ar-41, pCi/m3
I
II
III
[V
V
VI
VII
VIII
(BK6)
1015-1040
1048-1107
1113-1133
1142-1200
1203-1227
1230-1248
1321-1340
1404-1424
609 +_ 12
3082 +_ 21
2612 +_ 20
1477 _+ 14
844 +_ 12
442 +_ 10
12 + 2
1660 ^ 500
270 +_ 380
2340 +_ 750
1810 +_ 740
440 +_ 630
430 +_ 700
300 +_ 650
< 640
440
(e)
(e)
1060
610
320
(a)
(b)
(c)
(d)
(e)
(f)
See Appendix C for the detailed counting data.
All samples were collected on December 15, 1982.
The average net count rate for the detectors in Sectors III and
IV for the period indicated.
NR - Not reported.
Results used to determine the average Ar-41/cpm ratio of 0.72,
which was applied to the other period data to obtain the estimated
Ar-41 concentrations.
Concentrations from Table 3.4.
45
-------
3200
2800
2400
c
'£:
tf>
•*-*
3
o
o
i_
o
«
E
2000
I—
1600
O
Q.
1200
800
400
I
10:00
11:00 12:00 1:00
Time (A.M. - P.M.)
2:00
Fig. 3.7. The concentration of argon-41 as pCi/m3 ( — ) plotted with
the average net count rate of the rear two quadrants (counts/minute) of the
TRAC Plume Monitor.
46
-------
Because the Kr-85 concentrations were below the minimum detectable
level of the Penn State Noble Gas Monitor (see Appendix B), the compressed
air samples were returned to the EERF for cryogenic separation of krypton
and analyses by liquid scintillation counting (see Section 3.2.3).
However, because of inadequate purging, the scuba tanks contained residual
Kr-85 from earlier sampling, thus contaminating the SRP samples.
Therefore, Kr-85 measurements were not achieved.
The concentrations of tritium measured in the water vapor collected
from the atmosphere at sites 6 and 7 are listed in Table 3.6. Plant
personnel reported that all H-3 released from the reactor facilities is in
the oxide form (Ra82). Although no elemental tritium was detected in any
of the 1-liter grab samples collected, the total absence of elemental
tritium could not be confirmed because of the large MDL (2000 pCi/m ).
Site 6 was in the plume for less than half the sampling time indicated in
Table 3.6. However, the plume slowly fanned back and forth over the
collection trap at site 7 during nearly the entire sampling period
Table 3.6 Measured concentrations of HTO in the plume of the reactor facility
Site
6
7
Time of
Collection
1020-1230
1130-1345
pCi/ml
26
65
Tritium concentrations
g H20/m3 pCi/nr
10.0 260 + 100
10.0 650 + 100
Notes: 1) Discharge rate during sampling = 3.0 X 10 pCi/24 hours
= 347 nCi/sec (Ra82).
2) Chemical form: 100 percent HTO.
3) Collections made: 12/15/82.
47
-------
indicated. The collection traps at both sites became frozen during the
collection periods. Thus, the airborne H-3 concentration reported is
based on the concentration of H-3 in the water collected, and the relative
humidity and temperature provided by on-site meteorology. The water
content of the atmosphere during collection is also given in Table 3.6.
Collection site 7 was approximately the same distance from the
P-reactor stack as was site 4 from the H-Area stacks. Although 20 times
more tritium was being discharged from the latter during the respective
sampling periods (354 nCi/sec vs 7,130 uCi/sec), the H-3 measured in the
plume at site 4 was only 9 times greater than that measured in the plume
from P-reactor at site 7. This apparent discrepancy of a factor of 2 may
well be explained by differing plume dispersion characteristics and will
be considered further in Section 5. The measured environmental airborne
concentrations of both H-3 and Ar-41 will be compared in Section 5 to
computed concentrations derived from the measured source terms and
atmospheric dispersion models.
The concentrations of radioactive particulates measured in the plume
are shown in Table 3.2. No particulate radionuclides associated with SRP
activities were detected on filters from either site 6 or 7. This
indicates efficient control of particulate effluents from the stack and
helps to explain the low external gamma-ray exposures measured (see Table
3.3).
3.3 The Chemical Separation Facilities (F and H-Areas)
No reprocessing was being conducted at these facilities during the
period of the field study (see Section 2.3). Thus, although stack
effluent samples were collected later from one facility when it was again
in operation, January 19, 1983, no plume or environmental samples were
collected in the area.
48
-------
4. ENVIRONMENTAL MONITORING
t-.l Sample Collection
4.1.1 Vegetation and Sol 1 Samples. Vegetation samples were
collected on Plant property at sampling sites 4, 10, and 11 (see
2
Fig. 3.3). An area of either 1 or 4 m was measured and marked. The
vegetation within the area was clipped to near ground-level and bagged.
Eiecause of the season, most of the grass collected was not living. A
600 g soil sample was then collected to a depth of 2.0 cm within the area
from which the grass had been collected. All roots, rocks, and other
debris were removed from the sample.
Sampling site No. 10 was a cultivated field along the northeast side
of H Area. The site had been used to grow various food products to study
the uptake and transport of plutonium that had been deposited on the site
from an earlier H Area discharge. Site 10A was at the south end of the
cultivated field nearest the stack. Site 10B was in the approximate
center of the field, about ,50 m north of 10A. Vegetation at site 4 was
collected 10 m west of the tritium and participate samplers, while grass
at site 11 was collected at the 400 D monitoring station.
4.1.2 Food Samples. Foods that can be in the environmental pathways
from the Plant to the surrounding populations were sampled at off-site
locations. Collards were collected from two locations on 12/15/82;
Jackson, S.C, (site 13) and from 7 miles north of Aiken, S.C. (site 12).
A sample of beef was collected from a cow butchered on 12/16/82 that had
grazed near the intersection of Highways 19 and 302 (site 15). A 1-gallon
nrn'lk sample was obtained on 12/15/82 in Langley, S.C. (site 14). The
locations of these sample collection sites are in a northwesterly
direction from the plant site, which has a relatively high joint frequency
distribution that approaches about 9 percent (see Fig. 4.1).
49
-------
N
60 6 12 18 24
10 20 30 40
Fig. 4.1. The Savannah River Plant Site and surrounding area. Sampling locations are
outside plant site boundary and are designated by circled numbers with arrows pointing to
exact locations. Roads are designated by larger bold numbers. Letters designate site areas.
50
-------
4.2 Analyses
The grass and collard samples were freeze dried in order to measure
the tritium concentration in both the water and fibrous material. The
weights of the samples and sample fractions are listed in Table 4,1. The
tritium in the water fraction was measured directly by liquid
scintillation counting. Both H-3 and C-14 were measured in the fiberous
(freeze dried) material by combusting the material and collecting the
water and carbon dioxide. The H-3 in the water VMS again measured by
liquid scintillation counting and the C-14 was measured by converting the
COp to benzene and counting the C-14 associated with the benzene by
liquid scintillation techniques. The concentrations of gamma-ray emitting
nuclides in the freeze-dried samples were determined by gamma-ray
spectrometry using Ge(Li) detector systems.
The beef sample was also prepared for analyses by freeze drying after
being analyzed by gamma-ray spectrometry. The weights of the fractions
obtained are listed in Table 4.1. The tritium and carbon-14
concentrations were determined as described above.
Each of the food and environmental samples were analyzed for Sr-90
and the actinides. This was accomplished by dry ashing the freeze-dried
portion of each sample at 105Q°F (565°C) for 72 hours, dissolving the
ashed sample in acid, and performing the specified radiochemical
analysis. The procedures used are described in the EERF's Radiochemistry
Procedures Manual (L183).
The soil samples were weighed, dried at 125°C for 24 hours,
reweighed, and then ashed for 72 hours at 1050°F (565°C). One gram
aliquots of the soil samples were dissolved by treating with HF and
acids. Analyses of the dissolved samples were conducted as described in
the Procedures Manual.
4.3 Re su11s and Piscussion
The tritium concentrations in the grass and food samples are listed
in Table 4.2. There were measurable concentrations of H-3 in all samples.
51
-------
Table 4.1 Weights of environmental and food samples analyzed
Sample
Collards
Collards
Grass
Grass
Grass
Grass
Beef
Sampl e
No.
SRVL01
SRVL02
SRVP01
SRVP02
SRVP03
SRVP04
SRBF01
Collection (a)
Site
12
13
4
10A
10B
11
15
Fresh
wt., g
1687.4
1183.1
179
610
480.2
315.4
389.7
Freeze dried
wt., g
233.4
160.5
122.5
256
183.8
186.6
130.9
Water
Collected, ml
1390
1020
50
325
300
138
240
Percent
Water
86
86
32
58
62
41
66
See Figures 3.3 and 4.1 for site locations.
-------
Table t
Site
4
IDA
10 B
LI
12
13
15
14
L2 The tri
Sample
Type
Grass
Grass
Grass
Grass
Collards
Collards
Beef
Milk
tium concentrations in vegetation and
H-3 in
43 +_
2090 +_
53 +_
5.0 +_
0.51 _+
9.5 +_
0.6 +_
1.4 ^
Tri ti urn
Water
2
80
3
0.2
0.17
0.4
0.2
0.2
in 1.0 kg of fresh
Bound H-3
On-Site Samples
27 +3
146 +_ 15
47 +5
7.7 + 0.9
Off -Site Samples
0.17 + 0.02
0.95 +_ 0.10
0.5 ^0.2
ND
food samples
sample, nCi
Total 1
70 +_
2240 +_
100 +_
13 +_
0.7 +_
10 +_
1.1 +_
ritium
4
80
6
1
0.2
1
0.5
Note: ND - Not determined.
The higher concentrations occur in the grass samples collected near
H-Area; sites 4 and 10 relative to site 11 (see Fig. 3.3). The cause of
the significantly higher concentration in the grass from site 10A as
opposed to 10B is difficult to explain. A species difference as well as a
difference of 500 m distance from the stacks may partly explain the
twentyfold concentration difference. In general, more tritium was
associated with the plant water than the fibers, however, the winterized
condition of the grass probably affected the plant water content and,
thus, the quantity of tritiated water. Also, a few percent of the water
of combustion may have been inadvertently lost during combustion of the
dried fibrous material, which would tend to lower the amount of bound
tritium measured in the plant. Thus, there are some uncertainties in
these reported concentrations, but not of a nature to account for the wide
differences noted.
53
-------
Elevated levels of tritium were also measured in the off-site food
samples, which decreased with distance from the tritium producing areas
within the plant boundaries. The tritium concentration in the collards
sample collected near the site boundary at Jackson, site 13, was ten times
the H-3 concentration in a similar sample collected about 11 km north of
Aiken, S.C. The tritium in a sample of beef muscle that had been pastured
about 15 km north of the site boundary (site 15) was equally distributed
between the water and dried portions, and totaled about 1 nCi/kg fresh
weight. The water fraction of the milk sample from Langley contai-ned
about 1.5 nCi/1 of tritium. Thus, all environmental samples collected
from the vicinity of the SRP contained measurable amounts of H-3.
The radionuclide concentrations measured in the vegetation and soil
samples, except for H-3, are listed in Table 4.3. No significant
concentrations of gamma-ray emitting radionuclides were detected in either
the vegetation or soil samples. There was possibly a trace of Co-60 and a
137
somewhat elevated concentration of Cs in the grass sample from site
4, the more centrally located sampling location. However, in general, the
concentrations measured fall within the expected range of the natural
background. Potassium-40 is naturally occurring, Be-7, the most abundant
gamma-ray emitter observed in the vegetation, is cosmogenically produced,
and Cs-137 is primarily a fallout radionuclide that is readily absorbed by
certain plant species (Po67). Thorium-232 and Ra-226 were found to be in
the normal background range of 1 to 2 pCi/g (NCRP75).
The specific activity of C-14 is not greatly different in the four
grass samples. The average concentration is 18.8 ^1.2 dpm/g carbon,
which is only slightly higher (13 percent) and well within the uncertainty
of the natural specific activity reported by Eisenbud (1973), 7.5 +_ 2.7
pCi/g C or 16.6 ^ 6.0 dpm/g C. The NCRP (1975) reports the specific
activity to be 13.5 dpm/g C. The latter is a worldwide value taken from
UNSCEAR (Un77) and is lower than values reported by other authors (Ei73,
ORP73, Fr64). Therefore, considering the concentrations of C-14 measured
and the fact that they did not decrease with distance from the site
indicates that most of the C-14 observed was naturally (cosmogenetically)
produced with possibly a small contribution from Plant discharges.
54
-------
Table 4.3 Radlonuclide concentrations measured in vegetation and soil samples on site
Ol
tn
Collection Total veg.
Site^ Date Area, m^ sample, kg Analyses
4 12/14/82 4 0.18 Be-7
K-40
Co-60
Cs-137
C-14'a)
Sr-90
Pu-238
Pu-239
U-234
U-238
10A 12/16/82 4 0.61 Be-7
K-40
Cs-137
Ru~106.
C-14
-------
Table 4.3 (Continued)
01
o-l
Radionuclide concentration
Sited
11
(Bkgnd)
Notes:
(b)
1)
2)
3)
(a)
(b)
Collection Total veg.
Date Area, m2 sample, kg
12/16/82 1 0.32
See Figure 3.3 for site locations.
Tritium concentrations are listed in Table 4.2
NM - Not measured.
Concentrations of C-14 are presented as dpm/g
Background site for airborne effluents during
Analyses
Be-7
K-40
Cs-137
C-14'a)
Sr-90
Pu-238
Pu-239
U-234
U-238
.
Carbon.
collection periods.
vegetation,
pCi/kg fresh
3,400 +
2,100 +
130 +
17.7 +
490 +
<
0.7 +
13 T
12 T
700
900
50
1.4
50
0.7
0.5
2
2
Soil,
pCi/g dry
< 0.2
2.0 + 0.4
1.79 + 0.07
TTM
< 0.22
< 0.04
< 0.04
0.45 + 0.12
0.21 + 0.07
-------
The most predominant radionucTides, other than tritium, occurring in
the grass samples as a result of Plant operations were Sr-90 at site No.
4, U-234/238 at all sites, and Pu-238/239 at all sites except No. 11
[Table 4.3). No Sr-89 was detected in any environmental samples. Also,
Am-241 and Cm-242 were not observed {< 1 pCi/kg). The uranium content of
the grass does not appear to reflect soil concentrations and is probably
the result of deposition. Levels of uranium in the grass are higher near
the H-Area facility and, as in the soil samples, the isotopes are in
secular equilibrium. Of the gamma-ray emitters, only Cs~137
concentrations were elevated, primarily at site No. 4 where the soil
contained twice the Cs-137 than at other sites. Both Be~7 and K-40 have
natural origins. The higher levels of radionuclides associated with site
Ho, 4 are not surprising considering that the site is centrally located,
lying between the reactors and the production facilities (see Fig. 3.3).
The plutonium in the soil at sites IDA and 10B and, hence, in the
grass is primarily the result of an earlier uncontrolled plutonium release
that contaminated the soil at this site. The average gross alpha activity
of the soil at this site (~ 28 pCi/g) was about twice that measured at the
other two sites (~ 15 pCi/g), which provides further evidence of alpha
contamination. The Plant personnel are aware of this condition and have
jsed this area for study of the uptake of plutonium by several
agricultural crops. Resuspension of deposited radionuclides poses no
problem, due to a perpetual heavy cover of grasses.
The results of the food sample analyses, listed in Table 4.4, do not
indicate any gross contamination of the environment beyond the plant
boundary. The U-238 concentration in the collards averaged 0.6 _^ 0.3
pCi/kg fresh weight and was in equilibrium with U-234. The Sr-90
concentration in the collards grown at site No. 13 is twice that in the
slants grown at site Ho. 12. This difference, like H-3, may reflect plant
discharges, considering the closer proximity of site No. 13. However,
because natural variation in concentration can also account for this
difference, more analyses would be required in order to determine whether
•3!ant discharges are the source of Sr-90 in the collards from this site.
Strontium-90 in milk and beef are typical of ambient levels. A 1982
57
-------
Table 4.4 Radionuclide concentrations measured in foods collected near the Savannah River Plant
en
00
(a)
/ i \
(b)
/ \
(c)
(d)
Food , , Collection
Sample Site
-------
composite milk sample from the southeastern states was reported to contain
1.8 ^0.6 pCi/1 of Sr-90 (EPA83), exactly the concentration measured in
the milk collected from site No. 14. Strontium-90 levels in meat can vary
between 2-10 pCi/kg.
Thus, from the results of these few food type samples that were
raised near the site, only H-3 contamination can be linked unequivocally
to plant releases. The tritium levels are low and rapidly diminish with
distance from the site. The radiation dose equivalent due to tritium was
estimated for an individual who raises all foods near the Savannah River
Plant. The data used were as follows:
Food
Meat
Milk
Leafy vegetables
Annual(a)
Intake, kg
94
112
18
H-3,(b)
nCi/kg
1.1
1.4
10
pCi H-3 Intake/yr
1.03E+5
1.57E+5
1.80E+5
Source: EPA79.
Concentrations
4.;
4.4.
The total annual intake of tritium, 4.4E+5 pCi/yr, multiplied by the
whole-body dose conversion factor, 8.614E-8 mrem/pCi (Du80), yielded a
whole-body dose equivalent rate of 0.04 mrem/yr. This dose will cause no
significant health impact.
Although not confirmed by measurements, concentrations of C-14 and
plutonium may be slightly elevated above ambient levels in food samples
collected near the site due to plant releases. Carbon-14 measurements
indicate an excess of 1-2 dpm/gC above the natural level. This quantity
is equivalent to about 90 pCi/kg vegetables, 70 pCi/kg meat, and 40 pCi/kg
milk. Using these concentrations with the annual intake of foods given
above and a whole-body dose conversion factor of 1.58E-6 mrem/pCi (Du80),
yields a whole-body dose equivalent rate of 0.02 mrem/yr. Plutonium is
below the MDL in food type samples grown near the site boundary.
59
-------
5. MODELING
5.1 Predicted Airborne Concentrations
5.1.1 Results From EPA Modeling (Tritium measurements on 12/14/82).
Tritium oxide (HTO) was measured at site No. 3 from 1100 to 1410 and at
site No. 4 from 1120 to 1330 as described in Section 3.1.1. Ground level
concentrations normalized for source term x/Q were calculated for each
measurement interval. A summary of these calculated and measured X/Q
values are given in Table 5.1 for site No. 3. The azimuth angle of the
line drawn from H-Area release point to site No. 3 is 220°. During the
sampling interval at site No. 3, the plume azimuth angle varied between
186° (for the 1230 to 1245 meteorology) and 224° (for the 1400 to 1415
meteorology). A visual display of the relative orientation of release,
plume, and sampling site is given in Figure 5.1.
The average of the calculated X/Q values at site No. 3 was 8.7 x 10
O C -3
sec/m compared with a measured value of 2.8 x 10 sec/m . This
results in a ratio of the measured to calculated values of 3.2.
The azimuth angle of the line drawn from the H-Area release point to
site No. 4 is 209°. During the sampling interval at site No. 4, the plume
azimuth varied between 186° and 213°, thus sweeping over the sampling
point during the measurement. The average of the calculated x/Q values at
7 3
site No. 4 was 3.2 x 10 sec/m compared with a measured value of
7.7 x 10~ sec/m (see Table 5.2). This results in a ratio of the
measured to calculated X/Q of 2.4.
Argon-41 measurements on 12/15/82. Compressed air samples were taken on
12/15/82 at sites 6, 7, and 9 and analyzed for Ar-41. These measurements
were made to examine noble gas releases from P-reactor. Details of the
collection intervals and measured Ar-41 concentrations are given in Table
3.4. Ground level air concentrations normalized for source term x/Q were
calculated for each measurement interval.
As previously mentioned in Section 3.2.1, SRP's mobile gamma-ray
detection unit (TRAC vehicle) and a mobile PIC were used to verify the
60
-------
Table 5.1 Calculated and measured x/Q values for tritium at site No. 3 on 12/14/82
15 minute
interval
ending
1115
1130
1145
1200
1215
1230
1245
1300
1315
1330
1345
1400
1415
Wind*
azimuth
15
13
19
12
16
33
6
22
15
12
17
31
44
Wind
speed
mph
6.1
6.0
6.1
6.4
4.5
5.2
5.9
5.2
3.0
5.6
7.0
5.1
5.4
Horizontal
standard
deviation
a.
e
18.0
18.5
14.7
19.0
27.0
21.1
17.7
19.6
52.7
25.0
15.7
30.5
27.4
Vertical
standard
deviation
CJj
0
19.3
14.7
14.1
17.2
25.9
16.8
20.0
17.6
24.7
21.7
12.7
23.2
16.8
Calculated
Stability x/Q
class (sec/m3)
B
B
C
B
A
B
B
B
A
A
C
A
A
1.7 xlO-7
1.0 xlO-7
2.5 xlO'8
3.9 xlO-8
3.3 xlO-7
5.9 xlO'6
1.4 xlO-8
1.1 xlO-6
4.4 xlO-7
1.4 xlO-7
1.1 xlO'8
1.4 xlO-6
1.6 xlO-6
Average
X/Q
8.7xlO-7
Average
Concentra
(Ci/m3
1.98xlO-8
Measured
Source
tion Term
) Q (Ci/sec)
7.13xlO-3
X/Q Ratio
(sec/m3) Meas./Calc.
2.8xlO-6 3.2
* Hind azimuth + 180° = plume azimuth (see Fig. 5.1)
61
-------
N
RELEASE POINT
SAMPLING
SITE #3
y= 65m
SAMPLING
SITE #3
Fig. 5.1. Geometry of the plume for two representative tritium measurements
from H-Area on December 14, 1982.
62
-------
Table 5.2 Calculated and measured x/Q values for tritium at Site No. 4 on 12/14/82
Meteorological Data
15 minute
interval
ending
1130
1145
1200
1215
1230
1245
1300
1315
1330
Wind
azimuth
13
19
12
16
33
6
22
15
12
Wind
speed
mph
6.0
6.1
6.4
4.5
5.2
5.9
5.2
3.0
5.6
Horizontal
standard
deviation
°e
18.5
14.7
19.0
27.0
21.1
17.7
19.6
52.7
25.0
Vertical
standard
deviation
°0
14.7
14.1
17.2
25.9
16.8
20.0
17.6
24.7
21.7
Stabil
class
1130
1145
1200
1215
1230
1245
1300
1315
1330
ity
B
C
B
A
B
B
B
A
A
Calculated
x/Q
(sec/nr5)
(
i.eixio-7
5.73xlO~7
1.2 xlO'7
4.7 xlO~8
1. 05xlO-6
2.42x10-8
8.16xlO-7
6.45xlO-8
2.29x10-8
Average
value.x/Q
sec/m3)
3.2x10-
Average
concentration
(Ci/m3)
7 5.5xlO-9
Measured
Source x/Q Ratio
term (sec/m3) Meas./Calc.
Q (Ci/sec)
7.1xlO-3 7.7xlO~7 2.4
63
-------
position of the plume during each measurement interval. Use of this
instrument during the sampling proved most valuable because it
demonstrated that the plume position indicated by the 15-minute averaged
wind direction from P-area was not correct. Fortunately, use of this
instrument allowed a correction of the tabulated wind azimuth to be made.
This correction was made by adding the estimated azimuth error to the
tabulated wind azimuth to obtain a corrected value. The correction was
obtained as follows:
The X/Q measurement during the 11:13-11:33 internal at site No. 7
was found to be 1.9x10" (see Table 5.3) and corresponded to a
tabulated wind azimuth of 295°. However, the true azimuth to site
No. 7 is 323°. Both the measured x/Q and the gamma detection unit
verified the presence of the plume over site No. 7 during this
measurement interval. This indicates an error in the tabulated
plume azimuth for this measurement of (323°-295°) or 28°.
Therefore, 28° was taken as the constant error in azimuth angle
for all measurements from P-Area. (The magnitude of data taken
did not allow the authors to verify the constancy of the azimuth
angle error).
This apparent error in wind direction, as obtained from the P-Area
meteorological tower, is demonstrated in Figures 5.2 and 5.3, which show
uncorrected values for the 15 minute averaged plume azimuth compared with
true azimuth to the measurement site. It is evident that the measured
winds (arrows) were not in line with the site at which the plume's
presence was verified by measurements. Only once did the measured plume
direction coincide with the sampling site during the tritium collection
period (Fig. 5.2), and not once was there agreement during the argon-41
sampling periods (Fig. 5.3).
The effect of errors in wind direction on estimates of 15 minute
averaged X/Q'S can be significant for measurement points within a few
kilometers of the release point. The calculated X/Q is strongly dependent
on the off center line distance y:
v2
= K exp
64
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Table 5.3 Argon-41 measurements at sites 6, 7, and 9 on 12/15/82
Meteorological Data
15 minute
interval
endi ng
Wind Wind
azimuth, speed
(corrected) mph
Horizontal
standard
deviation
Vertical
standard
deviation
e
Site No. 6 (10:15-10:40 measurement)
1030
1045
134
139
8.8
9.8
12.6
9.8
9.7
7.8
1100
1115
Site No. 7 (10:48-11:07 measurement)
135
141
13.6
13.0
10.2
10.1
Site No. 7 (11:13-11:33 measurement)
1130
143
9.6
12.3
9.7
Site No. 7 (11:42-12:00 measurement)
1200
149
11.0
13.4
10.7
Site No. 7 (12:03-12:27 measurement)
1215
1230
147
153
9.6
9.7
13.8
17.5
10.7
12.2
Site No. 7 (12:30-12:48 measurement)
1245
152
12.2
15.9
12.2
Site No. 9 (13:21-13:40 measurement)
1330
1345
157
163
10.9
11.5
15.0
15.3
12.0
12.2
65
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Table 5.3(Continued)
Calculated Measured
15 Minute Stability x/Q Average Average Source x/Q Ratio
interval class (sec/m3) X/Q concentration term (sec/m3) Meas./Calc.
ending (Ci/m3) Q(Ci/sec)
Site No. 6 (10:15-10:40 measurement)
1030 C 1.4xlO-7 l.SxlO-7 1.7xlQ-9 1.23xlQ-3 1.4xlQ-6 7.9
1045 D 2.1x10-'
Site No. 7 (10:48-11:07 measurement)
1100 C 1.2xlO-6 l.SxlO-6 2.7xlO-10 1.23xlO-3 2.2xlQ-7 0.12
1115 C 2.4xlO-6
Site No. 7 (11:13-11:33 measurement)
1130 D 5.2xlQ-6 5.2xlO-6 2.3xlQ-9 1.23xlO-3 1.9xlQ-6 0.36
Site No. 7 (11:42-12:00 measurement)
1200 C 1.2xlO-6 1.2xlO-6 l.SxlO-9 1.23xlO-3 1.46xlQ-6 1.22
Site No. 7 (12:03-12:27 measurement)
1215 C 1.9xlO-6 1.2xlO-6 4.4xlO-10 1.23xlQ-3 3.6xlQ-7 0.30
1230 C 5.1xlO-7
Site No. 7 (12:30-12:48 measurement)
1245 C 5.4xlO-7 5.4xlO-7 4.3xlO-10 1.23xlQ-3 3.5xlQ-7 0.65
Site No. 9 (13:21-13:40 measurement)
1330 C 1.5xlO-7 S.lxlO-8 2.95xlO-10 1.23xlQ-3 2.4xlQ-7 3.0
1345 C l.lxlO-8
66
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SITE #7
(325°) 13:15
N
13:45 (315°)
13:30 (309°)
13:00 (3061
12:30 (305°)
12:45 (304°)
12:00 (301°
12:15(299°)
11:45(298°)
Azimuth to
site = 323°
Plume direction during tritium
sampling at site #7
P-area release point
Fig. 5.2. Schematic layout of release from P-Area and the measurement of
tritium at Site 7 on December 15,1982.
67
-------
N
SITE #7
12:30 (305°)
12:45 (304°)
12:00 (301°)
12:15(299°)
11:30(295°)
11:15(293°)
11:00 (287°).
Plume directions during argon-41
sampling at site #7
323°
Fig. 5.3. Schematic layout of release from P-Area and the measurement of
argon-41 at Site 7 on December 15,1982.
68
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Therefore, as y increases slightly, calculated x/Q decreases rapidly. An
example for the case of site No. 7 makes this point clear.
Consider the calculation of X/Q for Ar-41 during the 11:15-11:30
interval. For measured conditions at this point, a plume center line x/Q
a o
is 5.2 x 10 sec/m , whereas at 5° off center line the calculated
concentration is 2.2 x 10" sec/m , and at 10° off center line the
7 3
concentration drops to 1.6 x 10" sec/m . This behavior, shown in
Figure 5.4, indicates that the calculated plume concentration is
approximately reduced to half the center line value for a deviation in
plume direction of about 5°.
Results of calculated and measured x/Q values for Ar-41 are given in
Table 5.3. The azimuth angle of the line drawn from the P-area release
point to site No. 6 is 291°. During the sampling interval at site No. 6,
the plume azimuth (corrected as described above) varied between 314° and
319°. The average of the two calculated X/Q values at site No. 6 was
7 "3 f(
1.8 x 10" sec/m compared with a measured value of 1.4 x 10"
3
sec/m . This yields a ratio of measured to calculated X/Q of 7.8.
Five separate gas measurements were made at site No. 7 for Ar-41
(Table 3.4). The azimuth angle from the P-area release to site No. 7 was
323°. The plume azimuths (corrected) were as follows: first measurement,
315° and 321°; second measurement, 323°; third measurement, 329°; fourth
measurement, 327° and 333°; and the fifth measurement, 332°.
One measurement of X/Q was made at site No. 9 during the interval
13:21-13:40. The true azimuth to site No. 9 was 328°. During the
sampling interval, the plume varied from 337° to 343°. The average value
of calculated X/Q at site No. 9 was 8.1 x 10 compared with a measured
value of 2.4 x 10" . This yields a ratio of measured to calculated X/Q
of 3.0.
Tritium Measurements on 12/15/82. Tritium oxide was also measured downwind
of the reactor facility at site No. 6 from 1020 to 1230 and at site No. 7
from 1130 to 1345 (see Table 3.6 for a description of these measurements).
Similar to the previous case for argon collection, ground level tritium
concentrations normalized for source term were calculated for each
69
-------
7-
6-
5-
4-
3-
X10-'
O
-------
measurement interval, A summary of these calculated and measured X/Q
values are given in Table 5.4 for site No. 6. The azimuth angle of the
line drawn from the P-area release point to site No, 6 is 291°. During
the sampling interval at site No. 6, the plume azimuth (corrected as
described previously) varied between 314° and 333°.
The average of the calculated x/Q values at site No. 6 was
73 7
1.2 x ICf sec/m compared with a measured value of 7.5 x 10
3
sec/m . This implies a ratio of measured to calculated values of 6.3.
A summary of the calculated and measured x/Q values are given in
Table 5.5 for site No. 7. The azimuth angle of the line drawn from the
P-area release point to site No. 7 is 323°. During the sampling interval
at site No. 7, the plume azimuth varied between 326° and 353°.
The average of the calculated x/Q values at site No. 7 was
•70 c
7.4 x 10 sec/m compared with a measured value of 1.9 x 10
o
sec/m . This implies a ratio of measured to calculated values of 2.6.
5.1.2 [Results From DOE Modeling.* On December 14 and 15, 1983,
representatives of the U.S. Environmental Protection Agency (EPA) visited
the Savannah River Plant (SRP) to conduct independent measurements of
radionuclide concentrations in plumes emitted from SRP production areas.
The SRP assisted the EPA in this work. In particular, the Environmental
Sciences Division (ESD) of the Savannah River Laboratory (SRL) helped the
EPA position its samplers in the correct downwind trajectory forecasts and
real-time monitoring of the Ar-41 plume with the TRAC vehicle. The ESD
also gave the EPA representatives the meteorological data they needed to
test their own diffusion models.
The monitoring period on December 14 lasted from 1100 to 1410 EST.
During this period, the winds and turbulence were nearly steady, except
for small shifts in wind direction (15 to 20°) near the beginning and end
of the observation period. The emission rate of tritium from H-Area was
Q
estimated to be 7.1 x 10" Ci/s from daily average measurements. Since
only the average emissions and sampler data for the entire monitoring
This section is presented as prepared by the SRL,
71
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Table 5.4 Calculated and measured x/Q values for tritium at site No. 6 on 12/15/82
Meteorological
15 minute
interval
ending
1030
1045
1100
1115
1130
1145
1200
1215
1230
Wind
azimuth,
(corrected*)
134
139
135
141
143
146
149
147
153
Wind
speed
mph
8.8
9.8
7.0
8.9
9.6
9.2
11.0
9.6
9.7
Data
Horizontal
standard
deviation
12.6
9.8
13.6
13.0
12.3
14.6
13.4
13.8
17.5
Vertical
standard
deviation
9.7
7.8
10.2
10.1
9.7
10.2
10.7
10.7
12.2
Stabi 1 i
class
1030 C
1045 D
1100 C
1115 C
1130 D
1145 C
1200 C
1215 C
1230 C
Calculated
ty x/Q Average
(sec/m3) x/Q
1.4xlO-7
2.1xlO-7
1.7xlO-7
l.lxlO-7
1.4xlO-7 1.2x10-7
8.3xlO-8
5.9xlO-8
7.5x10-8
5.4x10-8
Measured
Average Source x/Q Ratio
concentration term (sec/m3) Meas./Calc.
(Ci/m3) Q (Ci/sec)
2.6xlO-10 3.5xlO-4 7.5x10-7 6.3
* See discussion of wind azimuth correction in Section 5.1.1.
72
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Table 5.5 Calculated and measured x/Q values for tritium at site No. 7 on 12/15/82
Meteorological
15 minute
interval
ending
1145
1200
1215
1230
1245
1300
1315
1330
1345
Wind
azimuth,
(corrected*)
146
149
147
153
152
154
173
157
163
Wind
speed
mph
9.2
11.0
9.6
9.7
12.2
15.6
13.2
10.9
11.5
Data
Horizontal
standard
deviation
CTe
14.6
13.4
13.8
17.5
15.9
12.9
13.0
15.0
15.3
Vertical
standard
deviation
aj
0
10.2
10.7
10.7
12.2
12.1
9.0
7.0
12.0
12.2
Stabi 1 i ty
ClclSS
1H5 C
1200 C
1215 C
1230 C
1245 C
1300 C
1315 C
1330 C
1345 C
Calculated
X/Q Average
(sec/m3) x/Q
2.2xlO-6
1.2xlO-6
1.9xlO-6
5.1xlO-7
5.4xlO-7 7.4xlO-7
2.3xlO-7
5.8xlO-12
l.lxlO-7
6.0xlO-9
Measured
Average Source x/Q Ratio
concentration term (sec/m3) Meas./Calc.
(Ci/m3) Q (Ci/sec)
6.5xlO-10 3.5xlO-4 1.9xlQ-6 2.6
* See discussion of wind azimuth correction in Section 5.1.1.
73
-------
period were provided, and the winds were steady, ESD made one calculation
of the plume concentrations. Winds and turbulence were also fairly steady
on December 15, when Ar-41 and tritium plumes from the P-Area reactor were
o
measured. The emission rate for Ar-41 was 1.0 x 10 Ci/s and the
emission rate for tritium was 3.5 x 10 Ci/s. One calculation was made
for the December 15 monitoring period, which extended from 1015 to 1345
EST.
The input data for December 14 and 15 are presented in Table 5.6.
These data are averages for the observation periods from the
Space-Average-Mean (SAM) data that is routinely generated by the SRL Wind
System. The plume rise calculations were based on the Briggs (1969)
formula for a nonbuoyant jet. Two of the H-Area stacks are 2.4 m wide,
with exit velocities of around 14 m/s. The third H-Area stack is 1.1 m
wide, with an exit velocity of about 9.4 m/s. Plume rise estimates were
based on the larger stack diameters and exit velocities. All stacks are
61 m tall. The P-Area stack is 5 m wide, with an exit velocity of around
3 m/s. A downwash correction for the P-Area stack on December 15 was
neglected, because it was only 5 m. The mixed-layer depth estimates were
based on observed temperature profiles from the 300 m WJBF-TV tower near
the SRP, and mixed-layer model predictions. The data in Table 5.6 were
the first and only estimates of the meteorological conditions during the
monitoring periods, i.e., there was no model "tuning" of any sort.
The SRL Wind System components, including the transport and diffusion
codes, are described by Garrett, Buckner, and Mueller (1983a) and by
Garrett and Murphy (1981). The diffusion code used here is a Gaussian
model modified to include removal by deposition. The diffusion rates are
determined from equations by Pasquill and Briggs. Table 5.7 summarizes
the calculations and includes the measured concentrations. The
Table 5.6 Meteorological input data for SRP calculations
Date
12/14
12/15
Wind
Speed
(m/s)
1.8
4.5
Wind
Direction
30°
140°
0e
29
14
°t
16
10
Mixing
Depth
(m)
600
500
Stack
Height
(m)
61
61
Plume
Rise
(m)
96
35
74
-------
calculations presented are for centerline maximum concentrations.
Trajectory errors could not be assessed, because only one sampling station
was used at each of the downwind distances where measurements were taken.
Calculated trajectories showed that the stations must have been close to
the center of the plumes most of the time. The measured values were taken
from data provided by the EPA. The results are presented in graphical
form in Figures 5.5, 5.6, and 5.7.
In Figure 5.5, the tritium concentrations measured on December 14 are
compared to the WIND System prediction. The error bars were determined by
the EPA. The averaging period was 2 to 3 hours, which, along with the
steady winds and turbulence, produced data appropriate for comparison to
Gaussian model predictions. The 25 percent underprediction at 1 km is
most interesting, because Gaussian models usually overpredict. Recently
developed diffusion models, which made use of convective boundary layer
scaling theory, also predict higher concentrations close to the release
point than the Gaussian model. Of course, there may be other factors
responsible for the underprediction, such as the plume rise estimate,
which was uncertain due to the different stack sizes in H-Area. To
summarize, the results from December 14 are very good, particularly since
there were only two sampling points.
Table 5.7 Summary of measured and calculated concentrations
Day
12/14
12/14
12/15
12/15
12/15
12/15
12/15
12/15
Station
3
4
6
7
6
7
7
9
Concentration (pCi/m )
Obs
19760+2800
5530+_ 810
260^ 100
650+_ 100
1662^ 502
890+_ 570
1304^ 690
295+ 648
Calc
15000
5500
510
510
1470
1470
1470
1000
Averaging
Time (min)
190
130
130
135
25
45
60
20
Distance
(km) Isotope
1.07
2.74
1.83
2.29
1.83
2.29
2.29
4.42
HT + HTO
HT + HTO
HTO
HTO
Ar-41
Ar-41
Ar-41
Ar-41
75
-------
20000 -i
15000 -
o
Q.
O
z
o
o
10000 -
5000 -
I
0.5
1 1.5 2
DISTANCE (km)
2.5
i
3
3.5
Fig. 5.5. A comparison of the December 14 EPA HTO measurements at H-Area with SRL calculated
concentrations.
-------
3000-1
2500-
2000-
•5
3 1500-
o
z
o
u 1000-
500-
I
3
DISTANCE (km)
Fig. 5.6. A comparison of the December 15 EPA argon-41 measurements at P-reactor with SRL calculated
concentrations.
-------
1000 I
800 -
oo
O
Q.
O
z
O
O
600-
400-
200 ~
0.5
I
1.5
I
2.5
DISTANCE (km)
Fig. 5.7. A comparison of the December 15 EPA HTO measurements at P-reactor with SRL calculated
concentrations.
-------
Figure 5.6 presents results from the Ar-41 measurements on December
15. Twenty-minute samples are indicated by dots, and 40- to 60-minute
averages of the 20-minute samples are indicated by X's. As expected, the
longer averages are in better agreement with model predictions, and
factor-of-2 agreement is achieved. Again, there is some underprediction
close to the release point for the 20-minute averages.
Figure 5.7 presents results from the tritium measurements on December
15. Both data points represent two-hour averages. The underprediction at
the 2.3 km station is so small {25 percent) that it can be attributed to
any number of things, such as the plume rise prediction, errors in the
wind speed and turbulence measurements, or fundamental limitations of the
Gaussian model.
5.1.3 Discussion. Two calculational procedures were used to estimate
plume concentrations and to determine their reliability by a comparison
v/ith measured concentrations. Both calculational methods estimated the
concentrations of tritium in the plume from H-Area within a factor of 3 of
the measured values. (Note—Agreement is generally considered good when
computed and measured concentrations differ by a factor of 3 or less.)
Attempts the following day to compute the tritium and argon-41
concentrations in the P-reactor plume demonstrated a misalignment of the
F-Area meteorological tower. Tabulated wind directions obtained from the
F'-Area were corrected by empirically locating the P-Area plume during the
measurement period. Using these corrected wind directions,
measured-to-calculated ratios of X/Q computed by the EPA method were
usually within a factor of 3; however, some were as high as 8. The
estimates of X/Q made by DOE did agree closely with measured values;
however, their procedure used average wind data for the complete
collection period (1015 to 1340) from all area meteorological stations and
assumed that the wind and plume directions were identical. The EPA
method, using only data from the nearest meteorological station at P-area,
had to be corrected for wind azimuth because of erroneously reported wind
directions from that station. The wind direction instrumentation at the
P-reactor station has subsequently been realigned (Ga83b).
79
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6. SUMMARY AND CONCLUSIONS
6cl General
A short-term one-visit field survey of airborne effluents was
conducted at the Savannah River Plant (SRP) during December 13-16, 1982.
The objectives of the survey were threefold: (1) to evaluate the
reliability of the radioactive discharges reported by SRP; ( 2) to
evaluate dispersion models by comparing measured radionuclide
concentrations in the plume with computed values; and (3) to measure the
concentrations of SRP related radionuclides in environmental samples
collected at and around the Savannah River Plant.
In general, the major objectives of the field study were
accomplished. Information was gained on environmental measurement
techniques, the limitations and usefulness of the airborne dispersion
models used to estimate environmental concentrations, and the extent of
environmental contamination that has resulted from airborne releases by
the SRP. These results are summarized briefly below.
An initial review of the surveillance program at the Savannah River
Plant showed that tritium is the principal radionuclide present in
off-site environmental samples due to plant releases. Radionuclides
contributing to the population exposures to a smaller degree are Ar-41 and
C-14. Particulate radionuclides appear to be effectively removed by
emission controls. Dose estimates were confirmed by three independent
models that gave similar dose equivalent rates for the principal
radionuclides (see Table 1.3).
Nearly all samples collected during the study were split and analyzed
separately by the EPA and SRP laboratories. Samples divided for
comparative analyses included samples of stack effluents, vegetation,
foods, and soil. Specific radionuclide analyses were performed, and the
results are compiled for comparative purposes in Appendix D.
In general, the analytical results reported by the two laboratories
are in good agreement. Values, invariably fall within or near the
80
-------
reported analytical uncertainties. The expected, small differences in
results were caused by the samples not being made homogeneous prior to
splitting, by the difference in elapsed time that occurred between sample
collection and analyses, and by small variations in laboratory procedures
and practices.
6.2 Source Term Evaluation
The release rate {source term) measurements generally agreed with
those reported by SRP (see Section 2.1.3 and Table 2.3). The tritium
release rates compared very well, differing by 20 percent at H-Area and
only by 2 percent at the P-reactor. The Ar-41 measurements were within 20
percent of the reported release rate, while other noble gas values agreed
within a factor of two or better. Considering that different measurement
techniques were employed by the two laboratories and that results from
continuous samplers were compared with "grab" samples analyzed by EERF,
the agreement is believed quite good. Thus, the release rates of
radionuclides that are reported by SRP and ultimately used for modeling
are considered reliable.
6.3 Plume Model Evaluation
The purpose of this evaluation was to determine how reliable plume
dispersion models are for predicting environmental concentrations of
radionuclides. For this purpose, tritium was measured at sites 3 and 4 in
the plume formed by releases from the H-Area stacks, and at sites 6 and 7
confirmed by TRAC measurements to be in the plume from the P-reactor
stacks. The rate at which H-3 was being discharged at the stacks was
monitored simultaneously with the plume measurements. The release rate of
Argon-41 was measured at the P-reactor stack and was included in the
evaluation by also measuring its concentration in the plume at sites 6 and
7. On-site meteorological data were used in the model calculations.
The measured and predicted plume concentrations of H-3 agreed within
a factor of 3 or better at sites 3 and 4. Most measurements at sites 6
81
-------
and 7 were also well within a factor of 3 of computed values; however,
some differed by as much as a factor of 8. Incorrectly reported wind
directions from the P-area were corrected using field measurements to
allow the computation of ground level x/Q. The reported wind directions
appeared to differ from the bearing of the actual plume by 18° to 36°.
Therefore, when using corrected meteorological data, computed and
measured concentrations were in reasonable agreement. When erroneous
meteorological data were used, large differences in measured and
calculated values resulted. For example, under the meteorological
conditions that existed during this study, a 10° error in the wind
direction would result in a thirtyfold error. The study demonstrated that
extreme care must be exercised to assure that the best and most
appropriate meteorological data are being used in modeling short-term
plume dispersion.
The ability to measure environmental concentrations of Ar-41, as well
as Kr-85, was also demonstrated. The TRAC Laboratory measurements were
well correlated with the Ar-41 and PIC measurements made in the plume.
The Penn State high-pressure gas monitoring system proved to be a valuable
asset to the study. Planning for future studies of this type, or of a
related nature, should consider the usefulness of a high-pressure gas
sampling system and include a concerted effort to coordinate closely field
measurements with the best available meteorology.
6.4 Environmental Contamination
Environmental sampling was limited to a few grass, soil, and food
samples. The on-site grass and soil samples contained quantities of
tritium, uranium, and plutonium that were clearly in excess of
background. An apparent excess of C-14 and Sr-90 in grass could not be
definitely established without further sampling. The levels of
contamination were largest in a location near H-Area known as the "farm".
The contamination observed in these samples was known to exist as a result
of earlier releases. In grass, uranium concentrations ranged up to 32
82
-------
pCI/kg, plutonium to about 15 pCi/kg, and tritium exceeded 2200 pCi/kg
fresh weight. Areas on which contamination has occurred are covered with
dense vegetation, thereby eliminating the transport of contaminants by
vnnd and water erosion to uncontrolled off-site areas.
Tritium was the only contaminant detected in off-site food products.
E'.ased on measured concentrations and the average annual intake of meat,
milk, and leafy vegetables, an individual eating foods produced near the
SRP site boundary would ingest about 440 nCi/yr of tritium. It was judged
that of the C-14 measured in food products grown near the site, 1-2 dpm/gC
could be due to Plant releases (see Table 4.3). Also, a plutonium
concentration in vegetation was estimated by extrapolation to be about 0.1
t'Ci/g. These concentrations in food products could result in dose
equivalent rates of 0.06 mrem/yr to the whole body due to H-3 and C-14,
and possibly as much as 0.2 mrem/yr to the endosteal cells from
plutonium. Thus, the food measurements that were made, although few in
number, indicate that airborne releases from the Savannah River Plant do
not significantly increase the radiation exposure to people living nearby.
83
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7. REFERENCES
As82 Ashley, C., Zeigler, C.C., and Gulp, P.A., 1982, "Releases of
Radioactivity at the Savannah River Plant 1954 through 1980,"
DPSU 81-25-1.
1 yq
Ba74 Bauer, F.P., 1974, "Environmental I Measurements," AEC Rept.
BNWL-SA-4983.
Br69 Briggs, G.A., 1969. Plume Rise. U.S. Atomic Energy Commission,
81 pp. Available as TID-25075 from Clearinghouse for Federal
Scientific and Technical Information, National Bureau of
Standards, U.S. Department of Commerce, Springfield, VA 22151.
Du82 Dukes, E.K. and Benjamin, R.W., 1982, "Savannah River Plant
Airborne Emissions and Controls", E.I. du Pont de Nemours and Co.
Report, DPST-82-1054.
Du80 Dunning, D.E., Jr., Leggett, R.W., and Yalcintas, M.G., 1980, "A
Combined Methodology for Estimating Dose Rates and Health Effects
From Exposure to Radioactive Pollutants," U.S. EPA Report,
ORNL/TM-7105.
Ea82 Eastern Environmental Radiation Facility, Office of Radiation
Programs, 1982, "The Quality Assurance Plan for the Eastern
Environmental Radiation Facility", QORM-001-82/1.
Ei73 Eisenbud, M., 1973, Environmental Radioactivity. 2nd Ed.,
Academic Press, New York, 187-188.
EP82 Environmental Protection Division, 1982, "Environmental Radiation
Surveillance Report, Summer 1980 - Summer 1982" Georgia
Department of Natural Resources, Atlanta, GA.
84
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REFERENCES-Continued
EPA79 Environmental Protection Agency, Office of Radiation Programs,
1979, "AIRDOS-EPA: A Computerized Methodology for Estimating
Environmental Concentrations and Dose to Man From Airborne
Releases of Radionuclides", EPA 520/1-79-009.
EPA83 Environmental Protection Agency, Office of Radiation Programs,
1983, "Environmental Radiation Data-Report No. 30."
Fr64 Friedlander, G., Kennedy, J.W. and Miller, J.M., 1964, Nuclear
and Radiochenristry, 2nd Ed., John Wiley and Sons, New York, 505.
Ga81 Garrett, A.J. and Murphy, C.E., 1981, "A Puff Plume Atmospheric
Deposition Model for Use at SRP in Emergency Response Situations,"
DP-1595, 76 pp., Savannah River Laboratory, Aiken, SC 29808.
Ga83a Garrett, A.J., Buckner, M.R., and Mueller, R.A., 1983, "The
Weather Information and Display Emergency Response System,"
Muclear Tech. 6p_, 50.
Ga83b Garrett, A.J., 1983, Sanannah River Plant, Aiken, SC, personal
communication.
Go75 Gold, S., 1975, "Analysis of Carbon-14 and Tritium in Reactor
Stack Gas", Environmental Protection Agency Report,
EPA-600/4-75-011.
HP82 Health Protection Dept., 1982, "Environmental Monitoring in the
Vicinity of the Savannah River Plant, Annual Report for 1981,"
DPSU 82-30-1.
ICRP75 International Commission on Radiological Protection, 1975,
"Report of The Task Group on Reference Man," ICRP Report No. 23.
85
-------
REFERENCES-Continued
Je80 Jester, W.A., _et _al_., 1980, "Monitoring Krypton-85 During TMI-2
Purging Using the Penn State Noble Gas Monitor", ANS/ENS
International Conference, Washington, D.C.
Ka82 Kantelo, M.V., Tiffany, B., and Anderson, T.J., 1982, "Iodine-129
Distribution in the Terrestrial Environment Surrounding a Nuclear
Fuel Reprocessing Plant after 25 Years of Operation", in
Environmental Migration of Long-Lived Radionuclides, (IAEA,
Vienna) pp. 495-500.
Ko81 Kocher, D.C., 1981, "Radioactive Decay Data Tables", Department
of Energy Publication, DOE/TIC-11026.
Li83 Lieberman, R., ed., 1983, "Eastern Environmental Radiation
Facility's Radiochemical Procedures Manual", Eastern
Environmental Radiation Facility Publication.
Ma63 Markee, E.H., 1963, "On the Relationship of Range to Standard
Deviation of Wind Fluctuations", Monthly Weather Rev. 91, 83.
Ma82 Marter, W.L., 1982, Savannah River Plant, Aiken, SC, personal
communication.
Mc76 McLendon, H.R., Stewart, O.M., Boni, A.L., Corey, J.C., McLeod,
K.W. and Pinder, J.E., 1976, "Relationships Among Plutonium Contents
of Soil, Vegetation, and Animals Collected Adjacent to an Integrated
Nuclear Complex in the Humid Southeastern USA," in Transuranium
Nuclides in the Environment. (IAEA, Vienna) pp. 347-363.
NCRP75 National Council on Radiation Protection and Measurements, 1975,
"Natural Background Radiation in the United States", NCRP Report No.
45.
86
-------
REFERENCES-Continued
ORP73 Office of Radiation Programs, EPA, 1973, "Carbon-14 in Total Diet
and Milk", Rad. Health Data Reports 14, 679-681.
Pe79 Pender, J.E., Smith, M.H., Boni, A.L., Corey, J.C.., and Norton,
J.H., 1979, "Plutonium Inventories in Two Old-Field Ecosystems in
the Vicinity of a Nuclear-Fuel Reprocessing Facility", Ecology 60,
1141.
Pe79 Pendergast, M.M., Boni, A.L., Ferber, G.J., and Telegadas, K.,
oc
1979, "Measured Weekly Kr Concentrations within 150 km of the
Savannah River Plant (March 1975 through August 1976)", DP-1486.
Po67 Porter, C.R., ej: j*l_., 1967, "The Cause of Relatively High Cs-137
Concentrations in Tampa, Florida, Milk", in Radiological
Concentration Processes, B. Aberg and F.P. Hungate, eds., Pergamon
Press, New York, 95-101.
Ra82 Ratchford, D.J., Savannah River Plant, personal communication,
December 8, 1982.
Ra83 Ratchford, D.J., Savannah River Plant, written communication,
January, 1983.
St71 Stevenson, D.L. and Johns, F.B., 1971, "Separation Techniques for
the Determination of Kr-85 in the Environment", in Rapid Methods
for Measuring Radioactivity in the Environment, IAEA, Vienna,
157-162.
Tu70 Turner, D.B., 1970, "Workbook of Atmospheric Dispersion Estimates,"
Office of Air Programs, U.S. Public Health Service, DAP-DTIP-AP-26.
87
-------
REFERENCES-Continued
Un77 United Nations Scientific Committee on the Effects of Atomic
Radiation, 1977, "Source and Effects of Ionizing Radiation",
United Nations, New York.
88
-------
APPENDIX A
RELEASE RATE OF RADIONUCLIDES
BASED ON WEEKLY COMPOSITED PARTICULATE AND
CHARCOAL SAMPLES FROM THE CHEMICAL
SEPARATIONS AND REACTOR FACILITIES
Samples Supplied by
D.J. Ratchford
Savannah River Plant
-------
Introduction
The following tables identify results of analyses of particul ate and
charcoal filters obtained from chemical separations areas F and H, as well
as reactors P, C, and K. These samples do not correspond to the time that
environmental samples were being collected and, consequently, do not
relate directly to the environmental study. They are included for
purposes of general information and for comparison with the other data, as
well as with results obtained by the Savannah River Laboratory for their
portions of the same samples.
A.I
-------
Table A.I Radionuclide Airborne Effluent Emissions from Chemical
Separations in F-Area
Radionucl ide
Co-60
Zr-95
Nb-95
Ru-103
Ru-106
Cs-137
Ce-141
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131
Concentration
(fCi/m3)
7 + 4
1,028 +_ 206
1,238 +_ 111
234 +_ 56
678 + 305
180 + 54
28 +_ 11
514 +_ 190
< 584
778 + 210
108 +_ 14
6 + 2
812 + 80
11 + 4
29 + 6
9 +_ 2
245 + 73
Release Rate
(pCi/s)
0.9 + 0.5
144 +_ 29
173 + 16
33 +_ 8
95 +_ 43
25 +_ 8
3.9 + 1.5
72 +_ 27
< 82
109 +_ 30
15+2
0.8 + 0.3
114 + 11
1.6 + 0.5
4.1 +0.9
1.2 + 0.2
34 + 10
These results are based on analyses of daily filter samples combined
for a period of one week. The fiberglass filters were cut in halves
and split between EPA and SRP. Particulate filters included a total
o
air volume of 856 m over the period of December 5 to 12, 1982.
The 1-131 results were from a charcoal sample that included a total
air volume of 2,181 m over the period from December 7 to 14,
1982. Errors shown are + 2a.
A.2
-------
Table A-2 Radionuclide Airborne Effluent Emissions from Chemical
Separations in H-Area
Radionuclide
Zr-95
Nb-95
Ru-103
Ru-106
Cs-137
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131
Concentration
(fCi/m3)
1,308 +
748 +_
981 ^
9,486 +_ 1,
70 +_
1,355 +_
183
97
108
043
57
298
< 1,170
< 234
17 +_
0.5 +
3.0 +
254 +
7 +
0.8 +_
< 150
3
0.3
0.8
28
1
0.5
Release Rate
(pCI/s)
183 +_ 26
105 + 14
137 + 15
1,328 + 146
9.8 +_ 8.0
190 + 42
< 160
< 33
2.4 +_ 0.4
0.07 + 0.05
0.4 +_ 0.1
35 + 4
1.0 + 0.2
0.11 + 0.07
< 21
These results are based on analyses of daily filter samples combined
for a period of one week. The fiberglass filters were cut in halves
and split between EPA and SRP. Particulate filters included a total
air volume of 428 m over the period of December 5 to 12, 1982.
The 1-131 results were from a charcoal sample that included a total
air volume of 856 m over the period from December 7 to 14, 1982
Errors shown are + 2a.
A.3
-------
Table A.3 Radionuclide Airborne Effluent Emissions from the P-Reactor
Radionuclide
All Y
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am -2 41
j_131(s)
I-131(d)
Concentration
(fCi/m3)
< 35
< 88
< 18
0.4 _+ 0.2
< 0.7
0.6 _+ 0.3
< 0.3
< 0.3
< 0.3
76.5^ 24.5
< 50
Release Rate
(pCi/s)
< 3
< 8
< 2
0.04 +_ 0.02
< 0.06
0.05 +_ 0.02
< 0.02
< 0.02
< 0.02
3.5 _+ 1.1
< 2
All results excluding 1-131 are from analyses of 72 mm diameter fiberglass
filters, including one from the stack sampling system and one from the
disassembly area exhaust sampling system. Particulate filters were split
with SRP and EPA, each receiving approximately half. Charcoal filters
included 155.7 g of charcoal in the stack sample and 148.5 g in the
disassembly exhaust sample. The charcoal samples were analyzed separately
for 1-131 in both the stack (s) and the disassembly exhaust (d). Both the
stack and disassembly exhaust sampling systems operated at 1 cfm flow rate
3
for a total sample volume of 285 m over the period from December 6 to
•3
13, 1982. Stack flow rate during this period was 46 m /s and the
o
disassembly exhaust flow rate was 42 m /s. Errors shown are + 2a.
A.4
-------
Table A.4 Radionuclide Airborne Effluent Emissions from the C-Reactor
Radionuclide
All Y
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
I-131(s)
I-131(d)
Concentration
(fCi/m3)
< 35
< 88
< 18
1 +_ 0.4
< 0.5
< 0.5
< 0.3
< 0.3
< 0.3
< 35
289 +_ 58
Release Rate
(pCi/s)
< 3
< 8
< 2
0.08 +_ 0.03
< 0.05
< 0.05
< 0.02
< 0.02
< 0.02
< 2
11 *_ 2
All results excluding 1-131 are from analyses of 72 mm diameter fiberglass
filters, including one from the stack sampling system and one from the
disassembly area exhaust sampling system. Particulate filters were split
with SRP and EPA, each receiving approximately half. Charcoal filters
included 111.6 g of charcoal in the stack sample and 162.7 g in the
disassembly exhaust sample. The charcoal samples were analyzed separately
for 1-131 in both the stack (s) and the disassembly exhaust (d). Both the
stack and disassembly exhaust sampling systems operated at 1 cfm flow rate
3
for a total sample volume of 285 m over the period from December 6 to
13, 1982. Stack flow rate during this period was 46 m /s and the
disassembly exhaust flow rate was 38 m /s. Errors shown are + 2a.
A.5
-------
Table A.5 Radionuclide Airborne Effluent Emissions from the K-Reactor
Radionuclide
All Y
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
I-131(s)
I-131(d)
Concentration
(fCi/m3)
< 35
< 88
< 18
0.8 +_ 0.4
< 0.5
0.6 +_ 0.3
0.5 ^0.3
< 0.3
< 0.3
26 +_ 21
< 42
Release Rate
(pCi/s)
< 3
< 7
< 2
0.07 _+ 0.03
< 0.05
0.05 + 0.03
0.04 +_ 0.02
< 0.02
< 0.02
1.2 _+ 1.0
< 1.6
All results excluding 1-131 are from analyses of 72 mm diameter fiberglass
filters, including one from the stack sampling system and one from the
disassembly area exhaust sampling system. Particulate filters were split
with SRP and EPA, each receiving approximately half. Charcoal filters
included 129.7 g of charcoal in the stack sample and 166.0 g in the
disassembly exhaust sample. The charcoal samples were analyzed separately
for 1-131 in both the stack (s) and the disassembly exhaust (d). Both the
stack and disassembly exhaust sampling systems operated at 1 cfm flow rate
3
for a total sample volume of 285 m over the period from December 6 to
o
13, 1982. Stack flow rate during this period was 46 m /s and the
disassembly exhaust flow rate was 38 m /s. Errors shown are + 2a.
A. 6
-------
APPENDIX B
USE OF THE
PENN STATE NOBLE GAS MONITOR
TO ASSAY
Kr-85 AND Ar-41 IN AIR SAMPLES
COLLECTED DURING THE
EPA SURVEY OF THE
SAVANNAH RIVER PLANT
Data Supplied by
William P. Kirk
U.S. EPA, TMI Station
-------
-------
Introduction
As part of the SRP survey, compressed gas samples were collected in
the plume from the operating P-reactor for a period of four hours on
December 15, 1982, and analyzed for Ar-41 and Kr-85 using the Penn State
Noble Gas Monitoring System. Additional Kr-85 analyses were done on the
same samples by cryogenic separation and liquid scintillation counting at
the Eastern Environmental Radiation Facility (EERF).
The Penn State Noble Gas Monitoring System was developed by Dr.
William Jester, Department of Nuclear Engineering, Pennsylvania State
University, several years ago for monitoring noble gases, particularly
Ar-41, inside reactor containment buildings. Subsequently, the system has
been used in the environment near several reactors and played a prominent
part in the Kr-85 monitoring program during the June 28-July 11, 1980,
purge of the containment building of the damaged Three Mile Island Unit II
reactor (1,2,3,4,5,6). The system, described in detail in the foregoing
references, utilizes a Windjammer Model 2310-00 5 CFM air compressor in
the field to fill scuba bottles to 3,000 psig (Vol. 80 ft.3, 2.3 m3).
The inlet hose to the air compressor contains a scrubbing train with
particulate filtration and activated charcoal to remove radioiodine. The
analytical part of the system consists of a roughly spherical 14.69 liter
high-pressure stainless steel vessel with reentrant well in its base to
permit insertion of a 10 percent efficient 50 cc Ge(Li) detector. The
counting chamber is mounted in a welded steel angle iron frame and
surrounded with 2 inches of lead (bricks) shielding. The detector is
coupled to any appropriate spectroscopic high voltage supply, preamp,
spectroscopic amplifier, multichannel analyzer, and output device such as
printer and/or magnetic tape/disc unit.
The MCA is appropriately energy calibrated, and a scuba bottle with
the compressed gas sample is cross-connected to the pressure chamber and
the pressure allowed to equilibrate. The end pressure is of the order of
1200 psig. The sample is then counted for an appropriate period, usually
20-30 minutes, and the specific activity of Kr-85 and/ or Ar-41
calculated, using the net activity in the 0.514 MeV and 1.293 MeV peaks,
respectively, and the volume (at STP) of gas in the counting chamber.
Calibration and calculation procedures are given in the references
(1,2,3,4,5,6).
B.I
-------
The Penn State System was used in this survey because of the need for
rapid, on-site analyses for Ar-41, whose 1.83 hr. half-life will not
permit returning the sample to the laboratory for elaborate separation and
analyses procedures. The Lower Limits of Detection (LLD) for Kr-85 and
3 3
Ar-41 with this System are about 50,000 pCi/m and 200 pCi/m ,
respectively. Since the cryogenic separation and liquid scintillation
analysis method employed by EERF can detect 2-3 pCi/m3 of Kr-85, the
analysis for that isotope with the Penn State System was only done because
it was concurrent with the Ar-41 determination.
Methods and Materials
The Penn State System was used as described in the basic references.
The spectroscopic system used consisted of a TRACOR TN1710 Analyzer, a
Canberra Model 3105 High Voltage Power Supply and a Canberra Model 2022
Spectroscopic Amplifier. Output was to a Texas Instrument "Silent 700"
printing terminal.
The basic calibration for the system had been previously determined
by Dr. Jester to be:
C = 6.6 x 108(ANJ pCi/m3 for Kr-85
P
C = 3.95x 107(AjO pCi/m3 for Ar-41
P
3
Where: C = Concentration in air of isotope in pCi/m .
AN = Net counts per second in the appropriate
peak.
P = Pressure in the counting chamber (psig).
These factors account for the counting efficiency of the system as
determined experimentally by evaporation of activation produced clathrates
of known activity into the chamber and counting as well as by use of NBS
sources.
B.2
-------
The Kr-85 calibration was checked at Penn State on December 6-7, 1982
by recounting, with the original Penn State setup, an environmental air
sample containing Kr-85 collected near Three Mile Island in July 1980.
The results demonstrated that the system efficiency had not changed since
the 1980 calibration and use. The EPA counting system was substituted for
the Penn State equipment and the sample recounted with the same result
within the statistics of the measurement.
The system was disassembled on December 8, 1982 and transported by
GOV (2 1/2-ton truck) to the Savannah River Plant where it was reassembled
on December 13, 1982 in Room 131, Building 735A (Environmental Laboratory
Building). The instruments were connected to a regulated laboratory
instrument circuit provided by SRP. The system was energy calibrated at
about 0.5 KeV/channel for 4096 channels on December 14, 1982 using check
sources containing Ba-133 (0.356 MeV), Cs-137 (0.662 MeV) and Co-60
(1.173, 1.332 MeV). The system parameters used are given in Table B.I.
Eight, 20 channel wide "regions of interest" were established as listed in
Table B.2. Regions were centered on the indicated energies.
Instrument background was determined for 40,000 seconds on the night
of December 14-15 with a 1200 psig air sample collected outside the SRP
environmental laboratory in the chamber and again for 50,000 seconds on
the night of December 15-16 with P-10 counting gas at atmospheric pressure
in the chamber. The energy calibration was checked on the mornings of
December 15 and 16. The centroids of Regions 1, 3, 4, 5 and 6 were
unchanged from the original calibrations.
The air compressor together with a rack containing 15 scuba bottles
was mounted in a 2 1/2-ton government-owned truck on December 14 which was
maneuvered as needed on December 15 to collect gas samples in the plume of
the operating P-reactor. Plume location was predicted by SRP
meteorologists and refined by the output of a large, directional NAI
system in the SRP plume monitoring van which accompanied the EPA team.
Scuba bottles were filled to 3,000 psig and immediately transported by
truck (SRP personnel) to Building 735A for counting. The collection
points and laboratory were 12-15 miles apart and samples were delivered to
the laboratory from 30-60 minutes after the end of collection.
B.3
-------
Table B.I Instrument settings-Room A131, Building 735A, SRP
Bias Voltage + 2800 V
Coarse Gain 100
Fine Gain .922
ULD 1.000
LLD 0.010
Zero 0.038
Polarity +
Bipolar Output:
4096 Channels - ~ 0.5 KeV/Channel
Table B.2 Spectral regions of interest setup in analyzer
Region Energy (MeV) Channels Isotope
0
1
2
3
4
5
6
7
1.293
0.356
0.514
0.662
1.173
1.332
1.462
1.593
2580-2600
709-729
1019-1039
1320-1340
2342-2362
2660-2680
2916-2936
3175-3192
Ar-41
Ba-133
Kr-85(a)
Cs-137
Co-60
Co-60
K-40
--
'a' Annihilation peak,
B.4
-------
A count time of 30 minutes was selected as a reasonable compromise
between the need for a long count, to improve statistics, and rapid
throughput to circumvent the 1.83 hour half-life of Ar-41.
Retrospectively, a 20 minute count would have been better because the time
required to bleed and purge the counting chamber after counting, to ensure
that no crossover between samples occurred, resulted in a gradually
increasing delay between collection and counting, thereby increasing the
probability of obtaining a statistically insignificant result for samples
that may have been significant if counted more promptly. Argon-41 results
were corrected for decay during counting and for the period from the
midpoint of collection to the start of counting.
Results and Discussion
The two background counts were statistically indistinguishable in all
8 regions. The mean value and composite standard deviation for each
region was used in all subsequent calculations. The mean of the two
overnight background count rates in the Ar-41 region was 0.0143 +_ 0.0008
ops.
Eight gas samples were taken and analyzed on December 15. Sample
No. 8 was an upwind background sample, while samples 1-7 were plume
samples. The results of counting these samples are given in Table B.3.
The only results that were statistically different from background were in
the Ar-41 region for samples 1, 3, and 4, which were all more than 4.66a
o;bove background, and the Kr-85 region for sample No. 8, which was
significantly below the nocturnal background.
Because the purpose of the Ar-41 determinations was to validate a
dispersion model and because the results obtained for the Ar-41 region
were all above nocturnal background (see Figure B.I), Ar-41 concentrations
were calculated and corrected for decay. Even though 4 of these samples
were not significantly above background when counted, it is probable that
counting immediately upon collection would have yielded a significant
result. For purposes of model validation, it is felt that the constructed
value at the midpoint of collection is more accurate than the "less than"
value that would normally be reported. The "constructed" values are
plotted in Figure B.2.
B.5
-------
Table B.3 The gamma-ray analyses of the compressed gas samples for Ar-41
Sample
No.
001
002
003
004
005
006
007
008
Collection
Site
6
7
7
7
7
7
9
8
Collection
Start
1015
1048
1113
1142
1203
1230
1321
1404
Period
Stop
1040
1107
1133
1200
1227
1248
1340
1424
Count Time^a
On
1111
1213
1317
1358
1448
1530
1612
1657
> Equil .
Pressure, psig
1210
1215
1210
1200
1200
1200
1190
1190
Total
Counts
89
34
83
66
34
33
31
27
Table B.3 The gamma-ray analyses of the compressed gas samples for Ar-41 (Continued).
CO
cn
Sample
No.
001
002
003
004
005
006
007
008
Gross counts,
cps
0.0494 +
0.0052
0.0189 +
0.0033
0.0461 +
0.0051
0.0367 +
0.0045 ~
0.0189+
0.0032
0.0183+
0.0032
0.0172+
0.0031
0.0150+
0.0029
Net counts, ^^
cps
0.035 +
0.005
0.0046+
0.0033
0.0318+
0.0051
0.0224+
0.0046"
0.0046+
0.0033
0.0040+
0.0033
0.0029+
0.0032
0.0007+
0.0030
Ar-41, (c)
1258 +
379
165 +
235
1140 +
366
809 +
333 ~
166 +
238
145 +
237 ~
106 +
232 ~
<220
Decay
Time, hr
0.73
1.27
1.90
2.12
2.55
2.85
2.70
2.71
Corrected
Ar-41 Conc.(d)
pCi/m3
1662 +
502
266 +
382
2343 +
752 ~
1806 +
743
436 +
627
427 +
702
295 +
648 ~
<640
Samples collected and counted on 12/15/82.
The mean background of 0.0143 +_ 0.0008 cps has been subtracted.
Corrected for decay during 30 minute counting period.
Concentration corrected to the midpoint of collection.
-------
Q
Z
o
o
UJ
V)
DC
IU
Q.
D
O
O
o
DC
(3
H
>
H
O
LU
Q.
0.10
0.09 •
0.08 -
0.07
0.06
O.OS
0.04
0.03
0.02
0.01
I I I I I I I I I
1 EJ
i i i
j I
I I
1 23456 78 BG-1 BG-2
SAMPLE IDENTIFICATION
Fig, B.-1. The gross count rate of argon-41 with 2-0 error bars. Also shown is the
mean nocturnal background ( — } with its 2-o uncertainty ( — )
B.7
-------
2800
2400
^ 2000
U
a
1600
1200 -
800
400
0
P U
a
Sample Identification
Fig. B.2. The net concentration of argon-41 corrected for decay to the midpoint
of collection.
B.8
-------
The low values obtained in the Kr-85 region for sample No, 8, a
background, led to a careful examination of the data from this region for
all samples. When compared to the combined nocturnal background data, six
of the eight samples were below the background, No. 8 significantly so,
and there appeared to be more variations than usual. Because of these
findings, malfunction of the MCA (or amplifier/preamp, power supply chain)
was suspected and data for each region of interest was plotted against its
own nocturnal background. The only two regions with variability beyond
statistical expectations were those for Ar-41 and Kr-85, which, together
with the constancy of the energy calibration, refutes the idea of system
malfunction. It appears, therefore, probable that there is some source of
photons in the 0.51-0.52 MeV range present at night at the location of the
counter, and the background in the Kr-85 spectral peak is considerably
lower than experimentally determined.
The observed random variability in the Kr-85 region is believed due
to contamination of the scuba tanks by residual Kr-85 from their earlier
use at TMI.
B.9
-------
REFERENCES
1. Jabs, R.H. and Jester, W.A., 1976, "Development of Environmental
Monitoring System for Detection of Radioactive Gases," Nuclear
Technology, Vol. 30, pp. 24-32.
2. Jester, W.A. and Hepburn, F.J., 1977, "A Ge(Li) System for the
Monitoring of Low Level Radioactive Gases," TRANS. ANS, Vol. 26, p.
121.
3. Jester, W.A. and Hepburn, F.J., 1977, "A Ge(Li) System for Monitoring
Low Levels of Radioactive Gases," Final Report Submitted to
Pennsylvania Power and Light Co.
4. Jester, W.A., Baratta, Jr., A.J., Granlund, R.W., and Eidam, G.R.,
1980, "Evaluation of Radiation Monitor Effectiveness for the
Detection of Krypton-85," TRANS. ANS, pp. 35, 57.
5. Jester, W.A. and Baratta, Jr., A.J., 1980, "Monitoring Krypton-85
During TMI Purging Using the Penn State Noble Gas Monitor," Final
Project Report to G.R. Eidam, Technical Coordinator, TMI Information
and Examination Program, EG and G, Idaho, Inc. (EG and G is DOE
Contractor, TMI).
6. Jester, W.A. and Baratta, Jr., A.J., 1982, "Monitoring Krypton-85
During the Three Mile Island Unit II Purging," Nuclear Technology
56: 478-483.
B.10
-------
APPENDIX C
THE TRAC LABORATORY
PLUME MONITOR
Data Supplied by
R.A. Sigg
Environmental Sciences Division
E.I. du Pont de Nemours and Co.
Savannah River Plant
-------
System Description
A plume monitor aboard the Tracking Radiological Atmospheric
Contaminants (TRAC) System gives the mobile laboratory an ability to
detect, locate and estimate concentrations of atmospheric radionuclides
emitting penetrating radiations. An array of twelve sodium iodide
detectors is the central component of the monitor, and is approximately
the same size used in aerial surveying and prospecting. Shadowing from
other equipment aboard the laboratory and interferences from natural
activities in the earth have been minimized by placing the array in a roof
level compartment and by shielding it along the bottom and sides. The
array is divided into four groups of three detectors by a cruciform
shield; count rate comparisons between these groups yields information
related to plume locations. Each detector has a 4 x 4 inch face, and each
quadrant contains a 4 inch, 8 inch and 12 inch long detector laying on its
side. The detector shield assembly and the data-acquisition electronics
assembly inside the laboratory are shock mounted for the mobile
application.
The TRAC System counting data listed in the following table were
collected simultaneously with the Ar-41 compressed air samples. Each
value listed is a 60 second count ending on the time indicated in the
second column. The first sector is directional toward the left front, the
second sector toward the right front, the third toward the left rear and
the fourth sector is directional toward the right rear. The sum of the
counts obtained in the four sectors is given in the last column of the
table.
C.I
-------
Table C.I Plume Measurements
Sampl e
Period
II
(b)
III
(b)
IV
Time,
Hours
(AM)
10.87
10.92
10.95
10.97
11.00
11.03
11.07
11.08
11.12
11.13
11.17
11.20.
11.22
11.24
11.27
11.29
11.32
11.34
11.37
11.40
11.43
11.45
11.48
11.50
11.52
11.55
11.57
11.60
11.62
11.66
11.68
11.71
11.73
11.75
11.78
11.81
11.83
11.86
11.88
11.91
11.93
11.96
11.99
Total
I
586
134
494
357
457
239
518
94
0
209
1627
1759
3749
3618
2485
3368
2461
2328
2454
3414
3427
2820
2829
2094
1932
1975
1705
561
617
1782
2466
3664
2932
3151
2884
2675
2337
2135
1440
2182
1471
2477
2131
Counts In
II
511
340
468
338
265
369
537
268
71
490
1595
1721
3395
3569
2520
3506
2354
2418
2783
3318
3855
2948
2888
2014
2201
2047
1377
435
713
1674
2273
3576
3017
2953
2408
2724
2556
2135
1697
2418
1704
2615
2503
Each
II
528
621
599
878
906
779
746
623
211
596
1773
2010
3921
3716
3023
3346
2686
2423
3219
3055
3638
3293
3421
2756
2885
2599
2178
717
1135
1912
2715
3630
3484
3445
3235
3133
2636
2181
1697
2265
1367
2335
2373
Sector*9)
I IV
593
483
732
639
596
963
780
347
151
601
1550
1687
3767
3730
2696
3441
2492
2474
2726
3401
3534
3282
3475
2708
2580
2336
1888
628
936
2478
2800
3907
3217
3421
2935
2988
2795
1909
1643
2152
1469
2054
2422
Total
Counts
2218
1578
2293
2212
2224
2350
2581
1332
433
1896
6545
7177
14832
14633
10726
13661
9993
9643
11182
13188
14454
12343
12613
9572
9598
8957
7148
2341
3441
7846
10254
14777
12650
12970
11462
11520
10324
8360
6477
9017
6011
9481
9429
C.2
-------
Table C.I Continued
Sample
Period
(b)
V
(b)
V!
(b)
VII
Ste
(PM)
12.01
12.03
12.06
12.08
12.11
12.13
12.16
12.18
12.21
12.25
12.27
12.29
12.32
12.34
12.37
12.39
12.43
12.46
12.48
12.51
12.54
12.56
12.58
12.62
12.64
12.67
12.69
12.72
12.74
12.77
12.81
12.83
12.86
12.88
1.35
1.39
1.42
1.53
1.56
1.60
1.62
1.65
1.68
Total Counts In
I
2122
1676
1342
1823
2907
1942
849
1644
1493
535
588
664
1123
2805
2781
2256
2389
1402
1297
769
448
432
157
892
2112
1249
860
2170
1040
615
784
554
246
0
594
142
175
370
172
567
599
390
565
I!
2033
2004
1658
2238
3496
2106
1070
1733
1288
622
665
629
1053
2882
2571
2252
2479
1716
1531
909
516
415
284
1138
2421
1829
1019
2208
992
582
895
628
205
55
563
328
307
462
509
623
543
565
744
Each Sector^
II!
1829
1448
1138
1713
2883
2001
372
1477
1498
343
598
740
1219
1627
1901
2214
2482
1721
1191
568
112
237
48
730
2052
1006
573
1938
940
507
831
516
130
0
698
217
341
440
357
450
595
355
659
IV
1895
1696
1066
2145
2829
1889
728
1613
1433
396
495
736
1099
1614
1771
2073
2586
1691
1541
610
413
271
263
881
1989
771
854
2337
1266
473
893
524
282
183
638
311
317
474
258
500
356
517
692
Total
Counts
7879
6824
5206
7919
12115
7938
3019
6467
5712
1896
2346
2769
4494
8928
9024
8795
9936
6530
5560
2856
1489
1355
752
3641
8574
4855
3306
8653
4238
2177
3403
2222
863
238
2493
998
1140
1746
1296
2140
2093
1827
2660
C.3
-------
Table C.I Continued
Samp! e
Period
(b)
VIII
lime.
Hours
(PM)
1.72
1.74
1.77
1.79
1.82
2.08
2.11
2.13
2.17
2.20
2.28
Total Counts In
I
759
728
834
547
524
68
0
0
0
9
0
II
948
548
860
626
542
35
11
17
71
0
0
Each Sector^
III
896
556
905
609
670
0
45
15
20
25
16
IV
933
697
639
573
773
0
0
0
0
13
16
Total
Counts
3536
2529
3238
2355
2509
103
56
32
91
47
32
Counts measured in 60 seconds on December 15, 1982.
Counts obtained between gas sampling periods.
C.4
-------
APPENDIX D
A COMPARISON OF THE
INTERLABORATORY ANALYSES
-------
Stack Effluent Sample Analyses
Stack effluent samples were collected from P-reactor and from the
F- and H-chemieal separations facilities. Samples collected were
participates, gases, condensed water vapor, and a charcoal filter sample
for radioiodine. The sampling procedures are described in Sections 2.2.2
and 2.3.2 of this report. Samples of each type were divided by SRP staff
for analyses by the two laboratories. Filters were split only
approximately into equal parts. Gas samples were collected consecutively
from the same port. The condensed water vapor samples were taken from the
same reservoir. Thus, only for the water sample was homogeneity of sample
assured.
The results reported by both laboratories are listed in Tables D.I,
D.2 and D.3 for comparison. The results of the EPA laboratory were taken
directly from Tables 2.2, 2.5 and 2.6 of Section 2, respectively. All
results of the P-reactor effluent samples are in good agreement. The
gross beta-gamma values reported by the SRP for the particulates agree
with the specific radionuclide analyses listed for the EPA laboratory.
Giood agreement also exists between the results reported for effluent
samples from the F- and H- facilities. Small differences in
concentrations of the alpha emitters may be due to an uneven distribution
of alpha-emitting particles on the filters. Differences in the reported
1-131 concentrations may also be the result of uneven distribution on the
charcoal filter. The SRP analyzed the whole charcoal filter before
splitting, while the EPA analyzed only a part of the filter at a later
date.
In addition to the split samples discussed above, daily particulate
filter samples were combined for a period of one week, cut approximately
in halves, and split between the EPA and SRP laboratories (see Appendix A
for a detailed description of these samples). The analytical results
reported by the two laboratories for the analyses of these samples are
listed in Tables D.4 through D.8. A comparison of these data show
reasonable agreement between the results for the analyses of stack samples
D.I
-------
from the three reactors (Tables D.4, D.5, and D.6). The results for
samples from the Chemical Separations Areas (Tables D.7 and D.8) show
general agreement except for some plutonium results and the EPA's values
for 1-131 are consistently lower than those reported by SRP.
Environmental and Food Sample Analyses
Samples of foods, vegetation, and soil were collected during this
study on or near the Savannah River Plant site and split for separate
analyses by the two laboratories. Detailed information on the collection
of these samples is given in Section 4 of this report. The environmental
sample splits were collected separately within a few meters of one
another. The food samples were collected by the SRP; the beef sample was
butchered from the same cow, the milk was obtained from a dairy, and the
col lards were from two farms. Neither the food samples nor the
environmental samples were homogenized before splitting. The analytical
results reported by the laboratories for these analyses are listed for
comparison in Tables D.9, D.10, and D.ll.
A review of the data in the tables show generally good agreement
between concentrations reported by the two laboratories. Differences in
the reported values for vegetation and food samples generally fall within
the two standard deviation error. The only exception is the reported
concentration of plutonium in the vegetation sample from Site 11. The
values reported by the EPA laboratory are significantly lower than those
given by the SRP. Site 11 was located near the Plant west boundary and
there would likely be less plutonium associated with soil and flora within
this area.
The EPA reported tritium concentrations in these samples on the basis
of fresh weight of sample in order to more easily compute the effective
dose to people eating the foods (see Table 4.2). However, the basic data
for tritium measured in the water fraction of these samples were available
enabling a direct comparison of the tritium concentrations measured by the
two laboratories. These concentrations are listed for comparison in Table
D.9. For most of the samples agreement was very good. Small differences
are observed only in the results for samples containing small quantities
of tritium.
D.2
-------
Summary
Agreement between laboratory analyses were generally good. The
largest observed differences were the values reported for plutonium and
1-131 in the week-long samples from F- and H-Area stacks. Small
differences in the results were expected considering the various time
delays between sample collection and analyses, differences in analytical
procedures and practices, and particularly the inhomogeneity of the split
samples.
D.3
-------
Table D.I Stack Effluent Samples from P-Reactor.
Type Sample
Radionuclide
EPA Measured
Concentration
(uCi/m3)
SRP Measured
Concentration
(uCi/m3)
Particulates
Particulates
Particulates
Particulates
Particulates
Particulates
Particulates
Particulates
Particulates
Charcoal
Water
Stack
Stack
Stack
Stack
Stack
Stack
Stack
Stack
gas
gas
gas
gas
gas
gas
gas
gas
Gamma emitting < 8E-8
Sr-89 < 4E-8
Sr-90 < 8E-9
U-234 < 3E-9
U-235 < 3E-9
U-238 (1.1 ±_ 0.3JE-8
Pu-238 < 1E-9
Pu-239 < 1E-9
Am-241 < IE -9
1-131 < 3E-7
H-3 (8.4^0.3)E+0
C-14 (7 _+ 2)E-3
Ar-41 (2.8^0.2)E+1
Kr-85 (1.2 +_ 0.2)E-5
Kr-85m (2 +_ 1)E-1
Kr-87 (1.4^0.9)E-1
Kr-88 (5 +_ 2)E-1
Xe-133 NM
Xe-135 (8 +_ 1)E-1
Gross
Beta-Gamma
< 2E-7
Total
Alpha
< IE -8
< 1E-11
(9.0 +_ 0.4)E+0
NM
(2.3 +_ 0.3)E+1
< 5E-2
(3 ^ 0.5)E-1
(1.3 +_0.2)E-1
(2 _+ 0.3JE-1
(3 +_ 0.5)E-1
(6 ^ 1)E-1
Notes: 1. Samples were collected during the following periods; particulates
from 0830 on 12/13 to 0830 on 12/16, water from 0830 on 12/15 to
0830 on 12/16, and stack gas at 1400 on 12/15.
NM - Not Measured
D.4
-------
Table D.2 Chemical Separations F-Area Stack Effluent Samples
R.adionucl ide
Zr-95
Nb-95
Ru-106
1-131
Cs-137
Ru-103
Ce-141
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131*
EPA Measured SRP Measured
Concentration (pCi/rn^) Concentration (pCi/m^)
1.04 + 0.06
1.24 +0.04
1.5 + 0.2
0.02 +_ 0.01
0.06 +_ 0.02
0.52 +0.04
0.03 +_ 0.02
0.58 +_ 0.08
< 2.0
< 0.4
0.11 +_ 0.03 •
< 0.033
1.2 ±0.2
0.01 +_ 0.01
0.02 +_ 0.01
< 0.001
0.07 + 0.01
1.5
1.4
2.3
<
<
0.71
<
0.38
0.24
0.6
0.028
0.042
0.07
0.8
+ 0.14
+_ 0.14
+ 0.86
0.10
0.13
+ 0.07
0.12
+_ 0.15
+_ 0.08
+ 0.01
+_ 0.004
+ 0.004
+_ 0.01
+ 0.02
Notes: 1. Particulate samples were split between SRP and EPA, and results
shown are estimates based on assumption of equal portions.
2. Particulates were collected during the period 0900 on 12/14 to 0900
on 12/15 and iodine was collected during the period 0900 on 12/7 to
0900 on 12/14.
* Charcoal filter sample. All other samples are particulate filters.
SRP analysis based on whole sample before splitting with EPA and
the values were decay corrected to the middle of the sampling
period.
D.5
-------
Table D.3 Chemical Separations H-Area Stack Effluent Samples
Radionuclide
Zr-95
Nb-95
Ru-103
Ru-106
Cs-134
Cs-137
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131*
EPA Measured SRP Measured
Concentration (pCi/nr*) Concentration (pCi/m^)
1.6 ^0.2
0.98 +0.09
2.9 +_ 0.2
31 + 1
0.082 + 0.005
0.23 + 0.05
2.3 ^0.7
< 8.0
< 1.6
0.04 +_ 0.01
< 0.0065
0.017 + 0.006
— t
0.22 +_ 0.03
0.003 + 0.002
< 0.0025
< 0.15
1.7 +0.3
0.7 + 0.3
3.1 + 0.2
31 + 1.8
< 0.18
< 0.26
2.9 + 0.04
0.82+0.12
0.02 +_ 0.001
0.13 +_ 0.07
0.01 +_0.01
0.02 + 0.01
0.74 +_ 0.60
Notes: 1. Particulates were collected during the period 0900 on 12/14 to 0900
on 12/15 and iodine was collected during the period 0900 on 12/7 to
0900 on 12/14.
2. Particulate filter samples were split between SRP and EPA, and
resuls shown are estimates based on assumption of equal portions.
* Charcoal filter sample. All other samples are particulate filters.
SRP analysis based on whole sample before splitting with EPA and
the values were decay corrected to the middle of the sampling
period.
D.6
-------
Table D.4 Radionuclide Airborne Effluent Emissions from the P-Reactor
Rc;dionuclide
EPA
Concentration
(fCi/m3)
SRP
Concentration
(fCi/m3)
All Y
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131^*
1-131^*
< 35
< 88
< 18
Gross
Beta-Gamma
< 33
0.4 +_ 0.2
< 0.7
0.6 +0.3
< 0.3
< 0.3
Gross Alpha
< 1.3
'
< 0.3
76.5 +_ 24.5 170 +_ 80
< 50 < 33
All results excluding 1-131 are from analyses of 72 mm diameter fiberglass
filters, including one from the stack sampling system and one from the
disassembly area exhaust sampling system. Particulate filters were split
with SRP and EPA each receiving approximately half. Charcoal filters
included 155.7 g of charcoal in the stack sample and 148.5 g in the
disassembly exhaust sample. The charcoal samples were analyzed separately
for 1-131 in both the stack^5' and the disassembly exhaust^). Both
the stack and disassembly exhaust sampling systems operated at 1 cfm flow
rate for a total sample volume of 285 m3 over the period from December 6
to 13, 1982. Stack flow rate during this period was 45 m3/s and the
disassembly exhaust flow rate was 42 m3/s. Errors shown are +_ 2a.
* 1-131 results were decay corrected to the middle of the sampling period.
D.7
-------
Table D.5 Radionuclide Airborne Effluent Emissions from the C-Reactor
Radionuclide
EPA
Concentration
(fCi/m3)
SRP
Concentration
(fCi/m3)
All Y
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
I_13l(s)*
1-131^*
< 35
< 88
< 18
1+0.4 J
< 0.5
< 0.5
< 0.3
< 0.3
Gross
Beta-Gamma
< 13
Gross
Alpha
< 1.2
< 0.3 '
< 35
289 + 58 590 + 470
All results excluding 1-131 are from analyses of 72 mm diameter fiberglass
filters, including one from the stack sampling system and one from the
disassembly area exhaust sampling system. Particulate filters were split
with SRP and EPA each receiving approximately half. Charcoal filters
included 111.6 g of charcoal in the stack sample and 162 g in the
disassembly exhaust sample., The charcoal samples were analyzed separately
~) anrl +ho Hi caccomhl v OYhanct(d) Rnth
for 1-131 in both the stack15' and the disassembly exhaust^
the stack and disassembly exhaust sampling systems operated at 1 cfm flow
rate for a total sample volume of 285 m3 over the period from December 6
to 13, 1982. Stack flow rate during this period was 46 m3/s and the
disassembly exhaust flow rate was 38 m3/s. Errors shown are +_ 2a.
1-131 results were decay corrected to the middle of the sampling period.
D.8
-------
Table D.6 Radionuclide Airborne Effluent Emissions from the K-Reactor
R.adionucl ide
EPA
Concentration
(fCi/m3)
SRP
Concentration
(fCi/m3)
All Y
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
I-131(s)*
I_13l(d)*
< 35
< 88
< 18
Gross
Beta-Gamma
< 38
0.8+0.4 J
< 0.5
0.6 + 0.3
0.5 + 0.3
< 0.3
Gross
Alpha
< 1.8
< 0.3
26+21 < 42
< 42 < 33
All results excluding 1-131 are from analyses of 72 mm diameter fiberglass
filters, including one from the stack sampling system and one from the
disassembly area exhaust sampling system. Particulate filters were split
with SRP and EPA each receiving approximately half. Charcoal filters
included 129.7 g of charcoal in the stack sample and 166.0 g in the
disassembly exhaust sample. The charcoal samples were analyzed separately
for 1-131 in both the stack^5' and the disassembly exhaust^. Both
the stack and disassembly exhaust sampling systems operated at 1 cfm flow
rate for a total sample volume of 285 nr over the period from December 6
to 13, 1982. Stack flow rate during this period was 46 m3/s and the
disassembly exhaust flow rate was 38 nr/s. Errors shown are +_ 2 a.
1-131 results were decay corrected to the middle of the sampling period.
D.9
-------
Table D.7 Radionuclide Airborne Effluent Emissions from Chemical Separations
in F-Area
EPA
Radionuclide Concentration
(fCi/m3)
Co-60 7 +_ 4
Zr-95 1,028 +_ 206
Nb-95 1,238 +_ 111
Ru-103 234 +_ 56
Ru-106 678 +_ 305
Cs-137 180 +_ 54
Ce-141 28 + 11
Ce-144 514 + 190
Sr-89 < 584 1
Sr-90 778 +_ 210 ]
U-234 108 +_ 14
U-235 6 + 2
U-238 812 + 80
Pu-238 11+4
Pu-239 29+6
Am-241 9 +_ 2
1-131* 245 +_ 73
SRP
Concentration
(fCi/m3)
< 14
873 +_ 40
1,040 + 20
200 +_ 20
520 + 190
157 + 10
53 + 30
380 + 60
670 +_ 120
870 +_ 108
152 + 20
220 +_ 28
35 + 24
1,760 + 820
These results are based on analyses of daily filter samples combined for a
period of one week. The fiberglass filters were cut in halves and split
between EPA and SRP. Particulate filters included a total air volume of
856 m3 over the period of December 5 to 12, 1982. The 1-131 results
were from a charcoal sample that included a total air volume of 2,181 m3
over the period from December 7 to 14, 1982. Errors shown are +_ 2a.
* 1-131 results were decay corrected to the middle of the sampling period.
D.10
-------
Table D.8 Radionuclide Airborne Effluent Emissions from Chemical Separations
in H-Area
Radionuclide
Zr-95
Nb-95
Ru-103
Ru-106
Cs-137
Ce-144
Sr-89
Sr-90
U-234
U-235
U-238
Pu-238
Pu-239
Am-241
1-131*
EPA
Concentration
(fCi/m3)
1,308 + 183
748 + 97
981 +_ 108
9,486 +_ 1,043
70 + 57
1,355 +298
< 1,170 |
< 234 ]
17+3
0.5 +_ 0.3
3.0 + 0.8
254 + 28
7 +_ 1
0.8 + 0.5
< 150
SRP
Concentration
(fCi/m3)
810 + 60
450 +_ 40
690 + 50
6,500 +_ 270
70 + 20
880 + 130
< 520
70 +_ 24
122 +_ 41
70 + 24
< 17
1,220 + 620
These results are based on analyses of daily filter samples combined for a
period of one week. The fiberglass filters were cut in halves and split
between EPA and SRP. Particulate filters included a total air volume of
856 m3 over the period of December 5 to 12, 1982. The 1-131 results
were from a charcoal sample that included a total air volume of 2,181 m3
over the period from December 7 to 14, 1982. Errors shown are +_ 2a.
* 1-131 results were decay corrected to the middle of the sampling period.
D.ll
-------
Table D.9 The Tritium Concentration in the Water of Vegetation and Food
Samples, pC/ml
Site
Samp!e
Type
EPA Measured
Concentration
SRP Measured
Concentration
4
10A
10B
11
Grass
Grass
Grass
Grass
On-Site Samples
153 +_ 1
3,919 +_ 6
85 +_ 1
11.4 + 0.4
120 + 1
3,600 + 2
75 +_ 1
4.9 + 0.4
Off-Site Samples
12
13
15
14
Collards
Col lards
Beef
Milk
0.6 +_ 0.2
11.0 + 0.4
1.0 + 0.2
1.2 + 0.2
0.7 + 0.4
12.0 +_ 0.5
0.02 + 0.33
0.6 + 0.4
D.12
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Table D.10 Radionucllde concentrations measured In vegetation and soil samples on site
EPA Radionuclide Concentration
SRP Radionuclide Concentration
Site Date Analyses
4 12/14/82 Be-7
K-40
Co-60
Cs-137
C-14(a)
Sr-90
Pu-238
Pu-239
U-234
P U-238
i— >
CO
10A 12/16/82 Be-7
K-40
Cs-137
Ru-106
C-14(a)
Sr-90
Pu-238
Pu-239
U-234
U-238
Vegetation
pCi/kg fresh
4,100 + 500
1,900 + 700
50 + 40
810 +_ 80
19.6 +_ 1.5
870 +_ 50
3.2 + 1.0
4.1 +_ 1.2
17 +_ 3
17 ± 3
2,300 +_ 300
1,500 +_ 600
420 + 60
< 60
18.0 + 1.4
210 +_ 30
4.3 +_ 1.0
7.5 + 1.5
7.7 + 1.4
5.6 + 1.1
Soil
pCi/kg dry
0.14 + 0.11
0.98 + 0.18
< 0.05
1.76 +_ 0.05
NM
< 0.23
< 0.03
0.04 + 0.02
0.67 +_ 0.10
0.70 + 0.10
< 0.2
3.6 +0.2
0.54 + 0.03
0.11 + 0.06
NM
< 0.10
0.67 + 0.14
2.2 +0.4
0.89 +_ 0.15
0.89 + 0.15
Vegetation
pCi/kg freshic)
5,900 +_ 13,700
10 +_ 15,000
5,200 +_ 16,300
700 +_ 130
NM
1,000 +_ 830
4.2 +_ 1.4
6.3 + 1.7
NM
NM
2,100 + 13,600
10 ± 15,200
1,100 + 1,400
10 + 12,000
NM
680 + 820
12 + 2.2
8.5 +_ 1.9
NM
NM
Soil
pCi/kg dry
< 0.13
0.6 +_1.2
0.14 + 0.38
1.1 +0.13
NM
NM
NM
NM
NM
NM
< 0.13
3.7 'jf 1.0
0.61 + 0.09
NM
NM
NM
NM
NM
NM
-------
Table D.10 (Continued)
EPA Radionuclide Concentration
Site
10B
Date Analyses
12/16/82 Be-7
K-40
Cs-137
C-14(a)
Sr-90
Pu-238
Pu-239
U-234
U-238
Vegetation
pCi/kg fresh
2,700 +_ 400
1,700 + 500
460 +_ 60
20.1 + 1.6
180 +_ 20
9.3 + 1.7
14.7 + 2.3
32 + 4
32 + 4
Soil
pCi/kg dry
< 0.2
1.08 + 0.16
0.49 +_ 0.03
NM
< 0.15
0.35 + 0.08
1.4 +_ 0.2
1.00 + 0.13
1.00 + 0.13
SRP Radionuclide
Vegetation
pCi/kg fresh(c>
8,700 +_ 14S000
4,400 +_ 15,600
1,000 +_ 1,400
NM
70 +_ 790
13 + 18
16 + 2.0
NM
NM
Concentration
Soil
pCi/kg dry
< 0.13
1.2 + 1.1
0.65 + 0.1
NM
NM
NM
NM
NM
NM
-------
Table D.10 (Continued)
en
EPA Radionuclide Concentration SRP
Site
11
(Bkgnd)
Notes:
Vegetation
Date Analyses pCi/kg fresh
(b)
1)
2)
3)
a)
b)
c)
12/16/82 Be-7 3
K-40 2
Cs-137
C-14(a)
Sr-90
Pu-238
Pu-239
U-234
U-238
See Figure 3.3 for site
Tritium concentrations
NM - Not measured.
,400 +_ 700
,100 +_ 900
130 +. 50
17.7 + 1.4
490 + 50
< 0.7
0.7 + 0.5
13 + 2
12 +_ 2
locations.
are listed in
Radionuclide Concentration
Soil Vegetation
pCi/kg dry pCi/kg fresh^
2.0
1.79
0.45
0.21
Table 4.
< 0.2 5,800
+0.4 1,900
+ 0.07 410
NM
< 0.22 230
< 0.04 3.6
< 0.04 4.4
+ 0.12
+ 0.07
2.
+_ 8,400
+ 920
+ 800
NM
+ 740
+ 1.6
+ 1.5
NM
NM
Concentrations of C-14 are presented as dpm/g Carbon.
Background site for airborne effluents during collection periods.
Results not comparable; SRP analyses were based on analysis of dried samples,
Soil
pCi/kg dry
< 0.13
1.3 +_ 1.2
2.2 +_ 0.15
NM
NM
NM
NM
NM
NM
whereas EPA
analyses were based on wet weight samples. SRP had only 20 grams of sample for analysis,
therefore, there are large counting errors involved.
-------
Table D.ll Radionuclide concentrations measured in foods collected near the Savannah River Plant
Food Collection
Sample Site*3' Date Analyses'0'
Collards 12 12/15/82 K-40
(pCi/kg) Cs-137
C-14(b)
Sr-90
Pu-238/239
U-234
U-238
Collards 13 12/15/82 K-40
o (pCi/kg) Cs-137
£ C-14(b)
Sr-90
Pu-238/239
U-234
U-238
Milk ' 14 12/15/82 K-40
(pCi/1) Cs-137
Sr-90
Pu-238/239
EPA
Concentration,
pCi/kg or liter
3,900 +_ 300
< 30
16.5 +1.3
99 + 14
< 0.70
0.4 +_ 0.2
0.5 + 0.2
5,400 +_ 400
< 30
16.7 + 1.3
190 +_ 17
< 0.70
NR(d)
0.8 + 0.04
1,200 + 200
< 10
1.8^0.7
< 0.7
SRP
Concentration,
pCi/kg or liter
2,800 +_ 170
< 98
NM(e)
120 +_ 60
< 0.8
NM
NM
5,300 +_ 200
< 98
NM
170 + 60
< 0.8
NM
NM
1,500 +_ 140
< 24
1.0^0.8
NM
-------
Table D.ll (Continued)
Food
Sample Site^a'
Beef 15
(pCi/kg)
(a) See Figure 4.1 for site
(b) Concentrations of C-14
o (c) Tritium concentrations
l> (d) NR - Not reported.
""""' (e) NM - Not measured.
Collection
Date
12/16/82
locations.
are presented
are given in
Analyses'0'
K-4Q
Cs-137
C-14
Sr-90
Pu-238/239
as dpm/g Carbon.
Table 4.2.
EPA
Concentration,
pCi/kg or liter
2,300 + 200
17 ± 7
18.7 + 1.5
5.5 + 1.2
< 0.3
SRP
Concentration,
pCi/kg or liter
1,470 +_ 420
0 +_ 30
NM
60+70
NM
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