1983-1988, annual average 3 H concentrations in 
the river (<200 pCi/L) were at least a factor of 
100 below the drinking water limit (Jaquish and 
Bryce, 1989). It is noteworthy that 3 H also 
occurs in the Columbia River upstream of Hanford. 
From 1983-1988, annual average 3 H concentrations 
in the river, upstream at Priest Rapids Dam, 
ranged from 70-100 pCi/L. 
Surface Water 
Columbia River water is used for drinking at 
downstream cities, for crop irrigation and for 
recreational activities (fishing, hunting, 
boating, waterskiing, swimming). Thus, it 
constitutes a primary environmental pathway to 
people for radioactivity in liquid effluents. 
Radionuclides can enter human foodstuffs through 
crops irrigated with river water and cow's milk 
through irrigated alfalfa and other cattle 
forage. Although radionuclides associated with 
Hanford operations, worldwide fallout and natural 
phenomena continue to be found in small but 
measurable quantities in the Columbia River, 
concentrations are below Washington State and 
Environmental Protection Agency (EPA) drinking 
water standards. 
Deep sediments in downstream reservoirs still 
contain low concentrations of some long-lived 
radionuclides (Nelson and Haushild, 1970; 
Haushild et al., 1975; Robertson and Fix, 1977; 
Sula, 1980; Beasley et al., 1981). Trace amounts 
of 239 Pu 60 Co, 137 Cs, and 152 Eu persist in sediments 
accumulated above the first downstream dam 
(McNary). In 1977, about 20 to 25% of the total 
plutonium inventory ( 239 . 240 . 241 p u ) i n Lake Wallula 
sediments, 100 km downstream, was believed to 
originate from the 1944 through 1971 releases at 
Hanford (Beasley et al., 1981). However, only 
239 Pu was believed to actually reflect earlier 
reactor operations. Furthermore, this 239 Pu was 
derived from 239 Np (produced by neutron capture in 
natural uranium followed by decay to 239 Np), an 
abundant isotope in Columbia River water. Thus, 
plutonium may not have been released to the river 
from reactor operations. 
Fish and Wildlife 
Fish are collected at various locations along the 
Columbia River and boneless fillets are analyzed 
for 60 Co, 90 Sr, and 137 Cs. Carcasses are analyzed 
to estimate 90 Sr in bone. Following shutdown of 
the last single-purpose, once-through cooling 
reactor and installation of improved liquid 
effluent control systems at N Reactor, short 
lived radionuclides, including the biologically 
important 32 P and 65 Zn, essentially disappeared 
from the river (Cushing et al., 1981) through 
radioactive decay. Radionuclide concentrations 
in fish collected from the Hanford Reach of the 
Columbia River are similar to those in fish from 
upstream locations. 
Deer (Odocoileus sp.), ring-necked pheasants 
(Phasianus colchicus), mallard ducks (Anas 
piatvrhvnchus), Nuttall cottontail rabbits 
(Svlvilagus nuttallii) and black-tailed jack 
rabbits (Lepus californicus) are collected and 
tissues are analyzed for ^Co and 137 Cs (muscle), 
239.240p u (-|-j ver ) anc | 90$ r (berne). The doses that 
could be received by consuming wildlife at the 
maximum radionuclide concentrations measured in 
1985-1988 were below applicable DOE standards 
(Price, 1986; PNL, 1987; Jaquish and Mitchell, 
1988; Jaquish and Bryce, 1989). 
Soil and Vegetation 
Airborne radionuclides are eventually deposited on 
vegetation or soil. Samples of surface soil and 
rangeland vegetation (sagebrush) are currently 
collected at 15 onsite and 23 site perimeter and 
offsite locations (Jaquish and Bryce, 1989). Sam 
ples are collected from nonagricultural, undis 
turbed sites so that natural deposition and 
buildup processes are represented. Sampling and 
analyses in 1985 through 1988 showed no radio 
nuclide buildup offsite that could be attributed 
to Hanford operations (Price, 1986; PNL, 1987; 
Jaquish and Mitchell, 1988; Jaquish and Bryce, 
1989). 
Foodstuffs 
The most direct way for deposited radionuclides to 
enter the foodchain is through consumption of 
leafy vegetables. Samples of alfalfa and several 
foodstuffs, including milk, vegetables, fruits, 
wine, beef, chickens, eggs and wheat, are col 
lected from several locations, primarily downwind 
(i.e., south and east) of the Site (Jaquish and 
Bryce,'1989). Samples are also collected from 
upwind and somewhat distant locations to provide 
information on radiation levels attributable to 
worldwide fallout. Foodstuffs from the Riverview 
Area (across the river and southeast) are irri 
gated with Columbia River water withdrawn down 
stream of the Site. Although low levels of 3 H, 
90 Sr, 129 I, and 137 Cs have been found in some food 
stuffs, concentrations in samples collected near 
Hanford are similar to those in samples collected 
away from the Site. 
Penetrating Radiation 
Penetrating radiation (primarily gamma-rays) is 
measured in the Hanford environs with thermolumi 
nescent dosimeters to estimate dose rates from 
external radiation sources. Radiation surveys are 
routinely conducted at numerous onsite locations 
including roads, railroads and retired waste- 
disposal sites located outside of operating areas. 
Onsite and offsite measurements and survey results 
for 1985-1988 were similar to past years. Dose 
rates near some operating facilities were only 
slightly higher than natural background rates. 
Overall Impact from Hanford Operations 
Beginning in 1974, evaluation of radiation doses 
has included assessment of the maximum external 
dose rate at a location accessible to the general 
public, doses to a hypothetical maximally exposed 
individual, and doses to the population within 
80 km (50 mi) of the Site. The calculated 50-year 
whole-body cumulative dose received by the maxi 
mally exposed individual ranged from 0.5 to 3 mrem 
during the years 1981 through 1986 (PNL, 1987). 
This hypothetical person receives the maximum 
calculated radiation dose using worst-case assump 
tions for location, inhalation of radioactive 
emissions, consumption of contaminated food and 
water, and direct exposure to contaminants. 
Expressed as effective dose equivalents, the 
calculated dose received by a hypothetical maxi 
mally exposed individual was 0.05 to 0.1 mrem 
annually from 1985 through 1988. The average per 
capita effective dose from 1985 through 1988, 
based on the human population of 340,000 within 
80 km of the Site, was 0.01 to 0.03 mrem annually 
(Price, 1986; PNL, 1987; Jaquish and Mitchell, 
1988; Jaquish and Bryce, 1989). Based on these 
assessments, potential radiation doses to the 
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