AECL-8364
ATOMIC ENERGY £ 2 ^ L'ENERGIE ATOMIQUEOF CANADA LIMITED T ^ 9 DU CANADA, LIMITEE
SOIL NUCLIDE DISTRIBUTION COEFFICIENTS
AND THEIR STATISTICAL DISTRIBUTIONS
COEFFICIENTS DE REPARTITION DES NUCLIDES DANS LE SOL
ET LEUR REPARTITION STATISTIQUE
Marsha I. Sheppard, Donald I. Beals, Denis H. ThibaultPatrick O'Connor
Whiteshell Nuclear Research Etablissement de recherchesEstablishment nucleaires de Whiteshell
Pinawa, Manitoba ROE 1 LODecember 1984 decembre
\Miuiv 1 nc:i; \ ol ( I mined. ll;,s4
ATOMIC ENERGY OF CANADA LIMITED
SOIL NUCLIDE DISTRIBUTION COEFFICIENTS
AND THEIR STATISTICAL DISTRIBUTIONS
by
Marsha I . Sheppard, Donald I . Beals, Denis H. Thibault
and Patr ick O'Connor
Whlteshell Nuclear Research EstablishmentPinawa, Manitoba ROE 1L0
1984 DecemberAECL-8364
COEFFICIENTS DE REPARTITION DES NUCLIDES DANS LE SOL
ET LEUR REPARTITION STATISTIQUE
par
Marsha I. Sheppard, Donald I. Beals, Denis H. Thibaultet Patrick O'Connor
RESUME
Les §valuations ecologiques de 1'evacuation des dSchets de combus-tible nuclSaire dans les formations de roche plutonique nScessitent uneanalyse de la migration des nuclides qui passent de 1*enceinte d1Evacuationa la biosphSre. Pour I1analyse de la migration des nuclides a travers 1'en-ceinte d'Svacuation, les matSriaux tampons et de remblayage, la roche pluto-nique et les raorts-terrains consolid§s et non consolidis, par l'entremise del'eau souterraine, on se sert de modules necessitant des coefficients derepartition (Kd) pOur decrire 1'interaction des nuclides et des materiauxgSologiques et artificiels. Ce rapport prSsente des coefficients de repar-tition dans le sol particuliers a certains elSments et leur ripartition dupoint de vue statistique, a partir d'une etude bibliographique en detail.Les elements radioactifs considers furent les suivants: actinium, ameri-cium, bismuth, calcium, carbone, cerium, cesium, iode, plomb, raolybdene,neptunium, nickel, niobium, palladium, plutonium, polonium, protactinium,radium, samarium, selenium, argent, strontium, technetium, terbium, thorium,etain, uranium et zirconium. Les el&ments stables consideres furent lessuivants: antimoine, bore, cadmium, tellure et zinc- Lorsque la disponlbi-lite des donn§es le permet, les coefficients de repartition et leur reparti-tion sont indiques pour les sols sabloneux, limoneux, argileux et organi-ques. L'utilisation de nos valeurs est recoramandee pour les evaluationseffectuSes dans le cadre du programme canadien de gestion des dSchets decombustible nuclgaire.
L'Energie Atomique du Canada, LimiteeEtablissement de recherches nuclfiaires de Whiteshell
Pinawa, Manitoba ROE 1L01984 decembre
AECL-8364
SOIL NUCLIDE DISTRIBUTION COEFFICIENTS
AND THEIR STATISTICAL DISTRIBUTIONS
by
Marsha I. Sheppard, Donald I. Beals, Denis H. Thibaultand Patrick O'Connor
ABSTRACT
Environmental assessments of the disposal of nuclear fuel waste inplutonic rock formations require analysis of the migration of nuclldes fromthe disposal vault to the biosphere. Analyses of nuclide migration viagroundwater through the disposal vault, the buffer and backfill, the pluto-nic rock, and the consolidated and unconsolidated overburden use modelsrequiring distribution coefficients (KJ) to describe the interaction of thenuclides with ;he geological and man-made materials. This report presentselement-specific soil distribution coefficients and their statistical dis-tributions, based on a detailed survey of the literature. Radioactive ele-ments considered were actinium, americium, bismuth, calcium, carbon, cerium,cesium, iodine, lead, molybdenum, neptunium, nickel, niobium, palladium,Plutonium, polonium, protactinium, radium, samarium, selenium, silver,strontium, technetium, terbium, thorium, tin, uranium and zirconium. Stableelements considered were antimony, boron, cadmium, tellurium and zinc.Where sufficient data were available, distribution coefficients and theirdistributions are given for sand, silt, clay and organic soils. Our valuesare recommended for use in assessments for the Canadian Nuclear Fuel WasteManagement Program.
Atomic Energy of Canada LimitedWhiteshell Nuclear Research Establishment
Pinawa, Manitoba ROE 1L01984 December
AECL-8364
TABLE OF CONTENTS
3.13.23.33.43.53.63.73.83.93.103.11
ACTINIUMAMERICIUMBISMUTHLEADNEPTUNIUMPOLONIUMPLUTONIUMPROTACTINIUMRADIUMTHORIUMURANIUM
1. INTRODUCTION
2. DISTRIBUTION COEFFICIENT, Kd 2
3. DISTRIBUTION COEFFICIENTS FOR THE ACTINIDES 5558810131720202326
4. DISTRIBUTION COEFFICIENTS FOR FISSION PRODUCTS 294.1 CALCIUM 294.2 CARBON 294.3 CESIUM 304.4 IODINE 334.5 MOLYBDENUM 364.6 NICKEL 364.7 PALLADIUM 374.8 RARE EARTHS - TERBIUM, SAMARIUM AND CERIUM 384.9 SELENIUM 394.10 SILVER 394.11 STRONTIUM 414.12 TECHNETIUM 464.13 TIN 494.14 ZIRCONIUM AND NIOBIUM 50
5. DISTRIBUTION COEFFICIENTS FOR OTHER NUCLIDES 515.1 ANTIMONY 515.2 BORON 515.3 CADMIUM 515.4 TELLURIUM 545.5 ZINC 54
5. CONCLUSIONS 56
REFERENCES 58
1. INTRODUCTION
Canada has selected geological containment in a vault deep in
plutonic rock in the Precambrian Shield as the most promising method for
disposal of its nuclear fuel waste (Boulton, 1978). A stable granitic
pluton will most likely be the host rock.
Assessment of the integrity of geological containment requires
pathways analysis to determine the travel time from the vault to the
biosphere of all the nuclides associated with the waste (Mehta, 1982). The
travel time and the predicted nuclide concentrations in the biosphere will
depend upon the interaction of the nuclides with their surroundings as they
migrate from the vault. Traditionally, this interaction has been described
using a distribution coefficient, K,, for rock, unconsolidated regolith and
soil (Wuschke et al., 1981). The objective of this report is to document
these K, values, separating them according to the major soil types found on
the Precambrian Shield. These parameter values are required for the soil
model in the assessment code used in the Canadian Nuclear Fuel Waste
Management Program.
Further, since the assessment code is stochastic, the
distributions of the K, values are also needed. Preliminary work with the
K values indicates that they are lognormally, as opposed to normally,ddistributed. The lognorraal distribution parameters (log^o) are reported
here. These parameters directly represent the data presented where two or
more values were found, and have not been adjusted toward conservatism for
assessment purposes. Sections A, 5 and 6 list the soil K, values, and their
appropriate distributions, for the actinides, the radionuclides produced
from nuclear fission and the stable nuclides, respectively, that are
expected to be present in 100-year cooled nuclear fuel (Mehta, 1982). A
reference list Is included for each nuclide.
- 2 -
2. DISTRIBUTION COEFFICIENT, K3
The processes of solute migration pertinent to radionuclide
migration in soil and unconsolidated geological materials have been discus-
sed and reviewed extensively (Wheeler, 1976; Onishi et al., 1981; Miller,
1983; Gillhara and Cherry, 1979; and Arnold et al., 1982). Many computer
models have been developed to predict nuclide migration through soil (Murali
and Aylmore, 1981; Yeh and Ward, 1981; Oster, 1982; Miller, 1983; Wong et
al., 1983; van Genuchten, 1978; Duguid and Reeves, 1976; and Sheppard,
1981). These models vary in their complexity and purpose. The simplest
model of the solute transport process, expressed in one-dimensional form,
is
where C is the solute concentration in solution, i.e., mass of solute
per unit volume of soil (g.cm~3),
t is time (s),
D is the dispersion coefficient (cm2.s-i),
x is the space coordinate (cm), and
V is the average linear pore-water velocity (cm.s-i).
Since Equation (1) does not account for the interaction of the solute and
the solid phase, the distribution coefficent, K , has been introduced tod
describe this interaction. The distribution coefficient is defined as the
concentration of solute in the adsorbed phase (mass of solute per unit mass
of soil) divided by the concentration of solute in the solution phase (mass
of solute per unit volume of soil pore water). The units of K are usually
mL/g. The K, value for each nuclide represents the partitioning of the
solute between the solid and solution phases and is applicable to equilib-
rium reactions, such as ion exchange.
Typical radionuclide interactions with soil include other geochem-
ical processes, such as precipitation, coprecipitation, hydrous metal oxide
- 3 -
coraplexation, organic matter complexation, colloid formation, and microbial
effects. Empirically determined K values may or may not include these pro-
cesses.
Ion exchange is one of the most common mechanisms of radionuclide
adsorption on geological materials (Ames and Rai, 1978). Thus, the K, value
depends upon several factors, including the cation exchange capacity (CEC),
and the species and concentration of both the ion being exchanged and the
competing ions. If the nuclide is present in smaller concentrations than
the competing Ions, then the K, value will be. independent of the concentra-
tion of the nuclide, and it will be constant if all other factors remain
constant (Johnston and Gillham, 1980).
To incorporate the K, concept into the solute transport process
described by Equation (1), the dispersion coefficient (D) and the pore-water
velocity coefficient (V) become the effective dispersion coefficient (D1)
and velocity coefficient ( V ) , respectively, where
• > • • !
'•4(2)
and R is the retardation factor, defined as
R = l + ^ K d (3)
where p, is the bulk density of the soil (g/cm3)
n is the porosity (cm3/cin3), and
K is the distribution coefficient (mL/g).
The K, concept is restricted to equilibrium reactions in which the concen-
trations in the solution and solid phases are related. K, was initially
defined by Mayer and Tompkins (1947) as
(4)
- 4 -
where C is the tracer concentration in the solution before adding the
sorbent,
C is the tracer concentration in the liquid phase of a sorbent-
water suspension,
V is the volume of liquid, and
M is the mass of solid.
Despite the fact that the K, concept strictly applies only to
simple cation-exchange, K, values are reported that describe more complex
reactions. This is in response to the need for input to simple migration
models. This report does not review the soil chemistry of the nuclides
considered; this has been done adequately elsewhere (Jenson, 1980; Johnston
and Gillham, 1980; Allard et al., 1977; Friedman, 1976, Swedish Nuclear Fuel
Supply Co. Ltd., 1983; Ames and Rai, 1978). The report does list all of the
K, values by predominant soil type for the Precambrian Shield (sand, silt,
clay and organic (Beals, 1984)) and includes other pertinent information
found in the literature. Table 1 lists K. distribution parameter estimates
for some nuclides combining all soils, as reported by Baes and Sharp (1981).
Nuclide
AmCeCsNpPbPoPuSrTcThU
* From Baes* * M o a n f\f t-1
ESTIMATES OF
p.**
2.93.03.01.02.02.73.31.4
-1.54.81.6
and Sharp (1981)
TABLE 1
DISTRIBUTIONS OF K,,*
1.30.60.81.00.70.31.00.90.50.60.6
exp( \i)+
(mL/g)
8101100110011995401800270.0360 00045
VALUES
K. Range(mL/g)
1.0 to 47 00058 to 600010 to 52 0000.16 to 9294.5 to 7600200 to 110011 to 300 0000.37 to 4000.003 to 0.282000 to 510 00011 to 4400
*** Standard deviation of the logarithm (to base 10) of K+ Median value of Kj with a 0.5 cumulative probability
- 5 -
3. DISTRIBUTION COEFFICIENTS FOR THE ACTINIDES
3.1 ACTINIUM
Nothing was found in the literature on K, values or the soil chem-
istry of actinium. We recommend using the K, values for americium because
of their chemical similarity.
3.2 AMERICIUM
Americium has been studied extensively because of weapons testing
in the 1950s. The summary on americium geochemistry presented by Johnston
and Gillham (1980) indicates that
(1) the most stable form of americium in aqueous solutions is Am 31";
(2) the soil sorption of americium is correlated to cation exchange
capacity, clay content, and concentration and type of the compe-
ting ions in solution, indicating that the principal retardation
mechanism is ion exchange;
(3) at high K, values, americium adsorption is sensitive to the con-
centration of americium in solution.
Table 2 lists the K, values reported by various investigators and includes
soil information (texture, pH, competing ions, etc.) pertinent to the sorp-
tion data. The recommended K, value means, standard deviations, ranges and
distribution parameters by soil type for americiura, based on Table 2, are
given in Table 3.
SoU 7. 7.T/ne &««) Silt
Sand fine sandyfine Randyfine sandyfine sandy
7.
d a y
loanloanloanloan
lL#it loanlLght loan
coarse sand
76.C 21.291.2 7.891.6 5.494.6 1.665.2 29.083.6 12.642.6 39.460.4 19.483.4 8.849.2 20.444.0 20.064.0 14.044.0 24.066.0 11.0?38-0 32.074.0 12.074.0 12.078.0 2.04S.0 34.0?82.0 9.0
Silt allty claysilty clay
loanI o n
16.0 50.09.0 54.0
H.0 53.0day
clay
5.0 31.032 X> 32.032.0 32.010.0 34.0
2.8
1.03.0
3,85.83 .8
18.020.2
7.822.436.022.032.023.030.014.014.020.018.09.0
loailcm
34.037.016J)
64.036.036.056.0
abyssal red clay
atyssal red clay
Organic organicorganic
XOrganic
2.4
2.45.75.78.48.4
-
0.431.190.990.210.450.170.600.180.160.982.4
3.40.20.30.1
0 . 30 .10 .70.7
0 . 6
2.82.82.52.50 . 8
2.33.60 .60.6
-
0.71.02.73.2-
-
40.840.8
7.
---
---
----
------
0.4
0.37.95.20.00.60.00.20.20.7
1.720.60.7
2.4
0 .0
0.00.9-
-
pH»Saturated Paste
5.3 (4.39)5.3 (5.71)5.0 (4.58)5.0 (6.17)6.0 (5.71)6.0 (6.72)
7-8
8.1
4 . 0
6.75.28.18.48.68.48.4
7.75.75.68.38 .0
7.5o.O8.25.46.4
4.85.9 (5-41)5.9 (6.56)6.7 (6.12)6.7 (6.98)
7.82.33.6
7.8 (7.12)7.8 (8.04)
7-3
7.94.85.46.22.7
6.9
7.2 (7.14)7.2 (7.54)
(V)
-------
----------
0.410.520.430.470.450.430.440.540.490.57----
0.440.570.56
-
0.420.490.450.57-
-
--
VALUES
CEC(nsqAOO
1515151515
15-
5.942.011.790.696.144.95
15.0410.446.38
18.3620.917.513.88.2
17.56.4
5.82.97.0
3.820202525
15.516.217.4
X30-
29.620.516.034.4
-
-
6060
FOR AMER1CILM :
I Freeg) Iron Oxides
1.651.651.521.525.295.29-
--------------------
1.291.292.412.41---
1.201.20-
-----
-
1.571.57
LXISAIURE SURVEY SLMWff
CompetingCation
-
-----
tb (90S s.-it.solution.)
---------------
---
--
-
Na (90* sat.solution)
----
0.68 mlA.NaQ
0.68 mol/LN a d
-
-
Kd(mL/g)
9.635xlO3
8.063xlO3
1.549xlO3
l,82xlO2
2.187x10"1.066x10"4xlO2
7.14xlO2
4.76xlO2
4.17xlO2
2.49xlO2
1.25xlO2
8.33xlO2
3.92xlO3
4.35x10"3.7x10"1.09x10"2.5xlO3 ± 210+6.CK1O2 ± 24+3.0xl02 • 10+8.2xlO2 ± 43+1.0x!0" ± l.SxlO1*1.2xlO2 ± 7+2.3xlO2 1 5+8.2x10' ± 1+**4.0xl02 t 11+3.9xlO2 • 2O*2.98x10"1.728x10"2.387x10"2.021x10"5.9xlO3 • 230*l.SxlO3*"1.6xlO3 • 190+3.563x10"4.723x10"5x10"
5.2xlO3 1 97C*2.6xlO3 1 47O1"9.2xlO2 • 79+2.9xlO3 t 1800+25.1
4.0xl05
7.266xlO3
5.529xlO3
Soil Locationor Inscription
rtilMs (Louisiana)btelbis (Louisiana)Lyaan (Milne)Lyman (Milne)Alken (California)Alken (California)(Netherlands)
(Rlchland, Washington)Fuquay (Bamuell, SC) O-5 enfcquay (Barmtll, SC) 5-15 oFuquay (Bamuell, SC) 15-50 cmftnf ord AHanf ord BIdaho AIdaho BIdaho CIdaho DColorado A (Bodty Flats)Colorado B (Sugar Loaf)Idaho BIdahoCIdaho Dttuhlngton A (Hanf ord)Uishlngton B (Itanford)S. Carolina (Bamuell)New Ifexico (Los ALaK*)Arkansas BSharpaburg (loua)Shafpsburg ( low)Yolo (California)Yolo (California)Idaho AArkansas CIllinoisHoltsvilleIbltsvllle(tetherLands)
Colorado C (Rocky Flats)Tennessee (Ok Ridge)New York (Vfest Valley)Arkansas A—
EgbertEgbert
Reference
NLshlta e t a l . 1979Nlshlta et a l . 1979Nishlta e t a l . 1979Nlshlta et a l . 1979Nlshlu e t a l . 1979Nlshlta et a l . 1979Hamcra 4 Verkerk, 1977
Azs I Rai, 1978Ana & Rai, 1978tees 4 ft.1, 1978a m & Rai, 1978A K S & Rai, 1978ABES 6 Rai, 1978
fees & Rai, 1978tees & Rai, 1978tuna 4 Rai, 1978tees & Rai, 1978Glover et a l . , 1976Glover et a l . . 1976Glover e t a l . , 1976Glover e t a l . , 1976Clover et a l . , 1976Glover et a l . , 1976Glover et a l . , 1976Glover et a l . , 1976Glover et a l . , 1976Glover et a l . , 1976Nlahitaet a l . , 1979Nlshlta et a l . , 1979.Vlshiu et a l . , 1979Nlshlta et a l . , 1979Glover et a l . , 1976Glover et a l . , 1976Glover et a l . , 1976NLshita et a l . , 1979KLshlta et a l . , 1979H n t r a I Verkerk, 1977
Glover et a l . , 1976Glover et al>, 1976Glover et a l . , 1976Glover e t a l . , 1976Erlckson, I960
Erlckson. 1980
NLshita et a l . , 1979NL.<hlta et a l . , 1979
* e n the value la bracketed, i t i s the ffl of the extract.S. Carolina subsoil K values for anerlclun w.r.t- calclvm and sodlun as competing ions over two orders of negnituJe are reported In Routson et a l .Kd value determined with init ial aDeridun concentration of 10"10 tnol/L.Sanrf, s i l t and clay percentages exceed 100X In original report.
1975.
- 7 -
TABLE 3
K, FOR AMERICIUM—a
SoilType
S.D."1
(mL7g)K, Range(mL/g)
LognormalDistribution*
Sand 6.146xlO3 1.1159x10** 27 82 to 4.35x10** 3.105 0.8172
Silt 1.4351x10** 1.1282x10** 7 1.6x103 to 2.98x10** 3.946 0.5382
Clay 6.0501x10** 1.29xl05 9 25.1 to 4.0xl0b 3.832 1.23
Organic 6.398x103 1.228x103 2 5.529x103 to 7.266x103 3.802 0.0839
* K = mean of K, valuesd d
"*" S.D. = standard deviation of K., valuesd
* Base 10 logarithms here and in all subsequent tables
Baes and Sharp (1981) suggested a mean value of 2.9 for the
logjgKj f° r ainericium, combining all soil types, and a corresponding stan-
dard deviation of 1.3 (see Table 1). Allard et al. (1977) reported K,d
values for clay/mud of 2 x 10 2 to 1.6 x 10 4 mL/g and for granite of
5.0 x 10 3 to 1.6 x 10 *• mL/g. Vandergraaf (198?) recommended a range of
1 x 103 to 2 x 10** mL/g for granite- The values for granite should be simi-
lar to those for coarse-textured soil (sand).
Americium References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and bedrock. Part 1. Determination of distributioncoefficients. ICBS Technical Report 55.
Ames, L.L. and D. Rai. 1978. Radionuclide interactions with soil and rock,media, Volume 1. U.S. Environmental Protection Agency Report, EPA520/6-78-007.
Baes III, C.F. and R.F. Sharp. 1981. Predicting radionuclide leachingfrom root zone soil for assessment applications. Trans. Am. Nucl. Soc.38, 111-112.
Erickson, K.L. 1980. Radionuclide sorption studies on abyssal red clays.In: Scientific Basis of Nuclear Waste Management Vol. 2. Plenum Press,ed. C.J.M. Northrup.
- 8 -
Glover, P.A., F.J. Miner and W.L. Polzer. 1976. Plutonium and americiumbehaviour in the soil/water environment. I. Sorption of plutonium andamericium by soils. In: Proceedings of the Actinide-Sediment Reac-tions Working Meeting at Seattle, Washington on 1976 Feb. 10-11. Bat-telle Pacific Northwest Laboratories Report, BNWL-2117, pp. 225-254.
Harastra, J. and B. Verkerk. 1977. Review of Netherlands program for geo-logic disposal of radioactive waste. Ini Nuclear Power and its FuelCycle. International Atomic Energy Agency Report, IAEA-CN-36/289.
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Nishita, H., A. Wallace, E.M. Romney and R.K. Schulz. 1979. Effect of soiltype on the extractability of 237Np, 239Pu, 241Am and 244Cm as a func-tion of pH. NUREG/CR-0997 UCLA 12-1192. 32 pp.
Routson, R.C., G. Jansen and A.V. Robinson. 1975. Sorption of 99Tc, 23^Jpand 2LflAm on two subsoils from differing weathering intensity areas.Battelle Pacific Northwest Laboratories Report, BNWL-1889.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
3.3 BISMUTH
Nothing was found in the literature on soil K, values for
bismuth, but bismuth should behave similarly to polonium because of their
proximity in the Periodic Table.
3.4 LEAD
Lead is a heavy-metal cation of general environmental concern in
most industrial areas. Consequently, considprgi-.le information exists about
its environmental behaviour (Gerritse et al., 1982; Wolf et al., 1977; Sol-
datini et al., 1976; Abd-Elfattah and Wada, 1981). Unfortunately, not much
K, information is available (see Table 4).
The recommended K, value means, standard deviations, ranges and
distribution parameters for lead by soil type, based on Table 4, are given
in Table 5-
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
K, VALUES FOR LEAD : LnBJAlUBE SUKVBf SIMWg
Sill X I X *Type Sand Stlt day Organic , Saturated Paslte (V)
CKC % Free(mcqAOO g) I ron ( M d e s
OpnpetingQatlon
Soil locationor Description
OrRanlc
0
0
20
inpol lutedorganic soil
unpolluted peat
unpolluted peat
polluted peatsphagnm pea:sphagnim peat
3.5
3.5
2.5
90
>90
>90
>90--
4.5-5.0
4.5-5.0
7.5-8.0
4.5
4-5
4-5
6.24-54-5
22
22
16
-
-
-
_
--
[ C a * J -O-0.015 HDI/L
[Ca21-)-0-0.015 nol/L
[&«•!-
0-0.015 m>L/L-
[ C a » ] -0-0.015 nol/L
[ & « • ] .O-0.015 molA.
--
2.8ilO2
1.3xlO3
3.5riO3
2.52x10^
1.8xl02
6.3X1O1*
2.34X101*61IO"
Soil C
SoU C
Soil D
SoU A
Feat A
Peat A
Soil 8
Iteference
Gerrttse et a i . , 1982
Gerrltse et a l . , 1982
Gerrltse et a l . , 1982
GerrltM et a l . , 1982
Gerrttoe et a l . , 1982
Gerrltse »t a l . , 1982
Gerrltse et a l . , 1982Vfolf e t a l . , 1977tolf e t a l . , 1977
I
I
- 10 -
TABLE 5
SoilType
Sand
Organic
(mL^g)
1693
2.7845x10 **
S.D.
1646
2.6024x104
n
3
4
KJ Range(mL/g)
280 to 3500
180 to 6.3x10h3
3
LognorraalDistribution
.035 0.5527
.954 1.150
Baes and Sharp (1981) suggested a mean value of 2.0 for the
log^0K, for lead, with a corresponding standard deviation of 0.7 (see Table
I). Lead should behave similarly to polonium and K values for polonium can
be found in Section 3.6.
Lead References
Abd-Elfattah, A. and K. Wada. 1981. Adsorption of lead, copper, zinc,cobalt and cadmium by soils that differ in cation-exchange materials.J. Soil Sci. 32_, 271-283.
Baes III, CF. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak. Ridge National Labora-tory Report, CONF-810606-44.
Gerritse, R.G., R. Vriesema, J.W. Dalenberg and H.P. De Roos. 1982. Effectof sewage sludge on trace element mobility in soils. J. Environ. Qual.1^, 359-364.
Soldatini, G.F., R. Riccardo and R. Levi-Minzi. 1976. Lead adsorption bysoils. I. Adsorption as measured by the Langmuir and Freundlich iso-therms. Water, Air Soil Pollut. 6 111-118.
Wolf, A., K. Bunzl, F. Dietl and W.F. Schmidt. 1977. Effect of calciumions on the absorption of lead (2+), copper (2-.), cadmium (2+), andzinc (2+) by humic substances. Chemosphere 6, 207-213.
3.5 NEPTUNIUM
The summary on neptunium geochemistry presented by Johnston and
Gillham (1980) indicates that
- 11 -
(1) neptunium should exist as Np in the form of NpO 2+ in an oxidi-
zing soil environment; however, it is not evident whether NpO J" is
also the dominant species under reducing conditions;
(2) neptunium colloids have been reported in some soil-solution exper-
iments (Sheppard et al., 1976) and absent in others (Routson et
al., 1977).
The recommended K value means, standard deviations, ranges and
distribution parameters for neptunium by soil type, based on Table 6, are
given in Table 7.
TABLE 7
FOR NEPTUNIUM
SoilType
S.D.d(mL/g)
^ Range
(mL/g)Lognormal
Distribution
Sand
Silt
Clay
Organic
37
471327
857
.6
.41
.
.5
9435
1529
101
.57
.88
.
.1
1764
2
0.16
1.27
41786
to
to
to
to
390
953200
929
0.6782
1.426
2.619
2.932
0.9728
0.6925
0.9222
0.0513
Baes and Sharp (1981) suggested a mean value of 1.0 for the
logi0K, for neptunium, with a corresponding standard deviation of 1.0 (see
Table 1). Allard et al. (1977) reported K ranges of 10 to 16 mL/g for
clay/mud and 25 to 50 mL/g for granites. Vandergraaf (1982) recommended a
K of 40 to 100 mL/g for granites,d
Neptunium References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and rock. Part 1. Determinations of DistributionCofficients. KBS Technical Report 55.
SoU X X XType Sand Sil t CLay
Sand fine sandy loamfine sandy loanfine sandy loanfine sandy loan
l l# i t loanlight loam
sandsandsandsand
sandy claysandy claysandy claysandy clay
76.0 21.2 2.894.6 1.6 3.8
sandSl i t s l l t y clay loan
s l l ty clay loanloanloan
12.6 65.8 21.632-0 56.0 12.0
Clay clayc Layclayclay
Organic organicorganic
7.Organic
2.42.45.75.78.48.4--------
0.430.210.392.82.82.52.53.610.840.60.60.860.29
40.840.8
X pH*CaXlj Saturated Paste
5.3 (4.08)5.3 (5.57)5.0 (4.42)5.0 (6.06)6.0 (5.56)6.0 (b.57)2 . 5 - 3.12 . 5 - 3.12 . 5 - 3.12.5 - 3.12 . 5 - 3.12 . 5 - 3.12.5 - 3.12 . 5 - 3.1
8.15.28.1
5.9 (5.83)5.9 (6.85)6.7 (6.13)6.7 (6.83)
5.36.5
7.8 (7.29)7.8 (8.28)
8.18.1
7.2 (6.24)7.2 C7.25)
Kj VALUES FOR NEPIUNIUM :
E^ CEC(V) (meq/100 g)
151515151515
--
------
5.940.69
0 sat.20202525
16.8810.76
3030
0 sat.0 sat .
6060
X FreeIron Oxides
1.651.651.521.525.295.29-----------
1.291.292.412.41--
1.201.20
-1.571.57 >
LTIERA1UKE SURVEY
CompetingCation
-
-----
0.002 m l / L Ca
0.2 O D I / L Ca
0.015 m l / L Na3 .0 mol/L Na0.002 mol/L Ca0 .2 mol/L Ca0.015 n c l / L Na3 .0 no l /L Na
---------------
sumuo
W g )
3183322610B2.370.363.93.20.250.160.70.415.432.4390 t 16359552811.2720.2411171950 ± 3103200 ±890786929
Soil Locationor Description
Milbis (Louisiana)Malbls (Louisiana)Lytmn (mine)Lyrnan (Msine)Aiken (California)Alken (California)Burtenk (Vhshlngton)Burbank (Washington)Burbank (Vhshlngton)Burbank (Vhshlngton)Scuth CarolinaSouth CarolinaSouth CarolinaSouth CaroLtnaBurtank (Rlchland, Vtahington)Fuquay (5-50 cm)K.E. Irish Sea SedinentSharpsburg (loua)Siarpsburg (lots)Yolo (California)Yolo (California)MiscatineRltzvrUleHoltsvllleIbltsvllleW Mediterranean sea sedimentNE Atlantic sea sedimentEgbertEgbert
Reference
Nlahlta et a l . ,Nlshlta et a l . ,Nlshlta et a l . ,Nlshlu et a l . .NLshlca et a l . .Nlshlta ec a l . ,Routson et a l . .Routson et a l . ,Routson et a l . ,Routson ec a l . ,Routson et a l . .Rcutson et a l . ,Rcutson ec a l . ,Routaon et a l . ,
19791979197919791979197919771977197719771977197719771977
tues I Ra?, 1976Ames & Rat, 1978Fowler & Aston,Nlshlu ec a l . ,Nlshlta et a l . ,Nlshlta et a l . ,NLshlta ec a l . ,
19821979197919791979
toes & Rat, 1978tos i Rat, 1978Nlshlu et a l . ,Nlshlta et a l . .Fowler 4 Aston,Fowler & Aston,Nlshlu et a l . ,NLshlU et a l . ,
197919791962198219791979
to
I
value Is bracketed It Is extract nH.
- 13 -
Ames, L.L. and D. Rai. 1978. Radionuclide Interactions with soil and rockmedia, Volume 1. U.S. Environmental Portection Agency Report, EPA52O/6-78-OO7 .
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Fowler, S-W. and S.R. Aston. 1982. Application of 23iftp in experimentalaquatic radioecology: Preliminary observations on neptunium behaviorin sea water, sediments and zooplankton. Health Phys. 4_2_, 515- 520.
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Nishita, H., A. Wallace, E.M. Romney and R.K. Schulz. 1979. Effect of soiltype on the extractability of 23^Jp, 2 3%u, 241Am and 21<Ltm as a func-tion of pH. NUREG/CR-0997 UCLA 12-1192. 32 pp.
Routson, R.C., G. Jansen and A.V. Robinson. 1977. 241Ara, 23^Ip and 99Tcsorption on two United States subsoils from differing weathering inten-sity areas. Health Phys. 33_, 311-317.
Sheppard, J.D., J.A. Kittrick and T.L. Hart. 1976. Determination of dis-tribution ratios and diffusion coefficients of neptunium, americium andcurium in soil-aquatic environments. Richland Operations Office Con-tract Report, RL0-2221-T-12-2.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
3.6 POLONIUM
Polonium information in the literature is extremely scarce.
Bismuth should behave similarly to polonium, and also lead and polonium
should behave similarly. All of the K, information on polonium reported
here (see Table 8) comes from one research program (Hansen, 1970; Hansen and
Watters, 1971). The chemical form of natural polonium in soils, resulting
from the decay of radium, may be similar to that of selenium (Hansen, 1970).
Tellurium is also a member of Group VIA of the Periodic Table and may behave
similarly to polonium. Polonium compounds with +2 and +4 oxidation states
have been reported, with the preferred oxidation state being +4 (Hansen,
1970). Polonium in air is generally found as polonium dioxide (PoO j)
* Unrestricted unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
TABLES
K, VALUES FTH FOLOKIW : UTHfflURE SURVEY SHUBX
Sail T. X Z Z Z fHTyj*s Sirei S t i c Q a y Organic CaCO3 Sa turated P a s t e
E CEC 1 Fcee Carpetingg ) I r o n CWdes Cfctian (mlig)
Soil Locationor Description Reference
42.0 3J.0 26.0 6.1 22.8
455459627295849597
%57
74
80
74
49
57
47
42222015180621
230
17
16
22
39
30
29
13242123105
1032
213
8
4
4
12
13
24
6.56.75.55.77.85.95.45.55.5
5.65.5
5.7
6.0
6.0
6.6
5.5
6.8
5.4----
3.02.61.81.5
4.6-
-
-
-
16.8
-
_ _
120
203
310
766
± 5*
±22
±41
I K S
1213 ± 186
643
723
192206508814275263525171555771713
30
66
75
254
371
137
±85
±83
±26± 11±34±42± 9
± 2± 3± 2± 1±0.6±17± 29± 1± 2
± 7
± 9
± 8
±22
±36
± 5
Him si l ty clay loam(All) (Colorado)
H n sl lty clay loam(A12) (Colorado)
rtftn s l l ty clay I o n(B,) (Colorado)
[ism sl l ty clay loam(S2t) (Colorado)
Hsm sl lty clay loan(BjCa) (Colorado)
Mxm allty clay loan(CCa) (Colorado)
DinflttOc alley city loss(C) (IOUB)
Lapeer loaa (Ap) (viaconsln)Lapeer loan (B2|) (Wisconsin)Lapeer loan (B29) (Ulaconsln)Lapeer loam (B3) (Utscoreln)lapser loan (C,) (Wisconsin)Adansville (A^ (Florida)BUnton (Ap (Florida)Lakeland (A[) (Horlda)Leon (Aj) (Florldz)Leon (A2> (Florida)Leon (Bn) (norlda)Leon (C) (Florida)RjsUn (A,) (Fkirliia)Darling gravelly sandy loan(B2) (Colorado)
Darling gravelly sandy l w(B,, r ) (Colorado)
Itorling gravelly sandy loan(C[) (Colorado)
Darling gravelly sandy loan(C2) (Colorado)
Gogebic sandy loam (ty(MLsconsiji)
Gogebic sandy loan (Bir)( « scons in)
Gogebic aandy loai (Birh)(Wlsccraln)
ftnsen & Vbtters, 1971
ttansen i Vbtters, 1971
Ifensen & Vfetcers, 1971
Hmsen t Wtcers, 1971
tensen t Vbtters, 1971
Fhnsen & Vbtters, 1971
Ihnsen I Vfctters, 1971
{fansen & Witters, 1971Hrasen 4 * t t « - » , 1971tenser & Vbcters, 1971Ifamen & o t t e r s , 1971Ansen 4 Vbtters, 1971•Ansen i Vhtters, 1971ibnsen & Vbtters, 1971Hansen & Witters, 1971tfensen & Witters, 1971Hansen i Vbtters, 1971Ifensen f. Vbtters, 1971Hansan i Vbrters, 1971Hmsen & Vbtters, 1971Hamen I Vbttzrs, 1971
Ifanscn t vktten, 1971
Hmaen I Vbtten, 1971
Hmsen 4 Vbttera, 1971
Vhnsen I Vbtters, 1971
Hmsen 4 Vbtters, 1971
Iknssi i Vhtters, 1971
(contlimKl...)
TABLE 8 (Condir ied)
S o i l X X X X XType Snrxl Silt day Organic CaO03 Saturated P&slte (V)
CEC X Free Carpeting K,(raeqAOO g) Iron Ojddes Cation (ni./g)
Soil Location
or Description
68
46
46
67
67
82916311
17
3
10
U
10
8
5
2
5
5
33
27
27
44
43
20
20
50
2768
55
73
61
65
80
71
66
66
65
66
52
55
5
10
11
13
13
139
1021
28
24
29
24
10
21
29
32
30
29
15
18
3.8
5.9
6.8
6.9
8.2
8.4
6.35.05.65.8
5.6
5.5
5.9
7.8
5.9
6.2
6.1
5.6
5.3
5.5
5.1
5.5
5.1
-
-
-
2.71.93.4
25.2
-
2o.4
-
-
11.2
-
-
-
-
-
28.9
16.4
242 ± 25
227 ± 20
412 ± 150
2248 ± 1200
7020 ± 3600
76 ± 11188 ± 1549 t 31030 ± 49
976 ± 127
1136 ± 118
968 ±32
1830 ± 210
970 ± 160
122+3
92 ± 3
597 ± 55
80 ± 2
772 ±29
24 ± 1
405 ±28
Gogebic sandy loan (B3)(Wisconsin)
Onaway fine sandy loan (Ap)(Wisconsin)
Onaway fine sandy loan (BLrh)(Wisconsin)
Onauay fine sandy loam (Cj)(Wisconsin)
Onauay fine sandy loan (Cj)(Wisconsin)
Anite (A;) AlabaoBIndependence (AL) (Alabana)Wlckhan (A,) (Alabama)Dinsdale s l l ty clay loam(A) (lew)
Dinsdale s l l ty clay loan(B) (loua)
Miscatine s l l ty clay loan(A) (low)
Hiscatlne s l l ty clay loan(B) (loua)
Miscatine s i l ty clay loao(C) (Ioua)
Fayette s i l t loan (Ap)(Wisconsin)
Fayette l i l t loan (Bj)(Wisconsin)
Fayette s i l t loan (BJJ)(Wisconsin)
Fayette s i l t loan (B22)(Wisconsin)
Fayette s i l t loan (B23)(Wisconsin)
Fayette s i l t loan (C,)(Wisconsin)
Darling gravelly sandy loam(Aj) (Cblorado)
Cbngaree (A.) (Alabana)
Hansen & Witters, 1971
Hansen & Vbtters, 1971
Hmsen & Ifetters, 1971
ftmsen «. Wattera, 1971
Hmsen 5 l i t t e r s . 1971
Hmsen i Hatters, 1971Hansen i Witters, 1971Hmsen & Hitters, 1971Hansen & Matters, 1971
Hansen & Hatters, 1971
Hareen I Hitters, 1971
Hansen 6 Hitters, 1971
Hansen & Hitters, 1971
Uansen £ Hitters, 1971
Hansen & Hitters, 1971
Hansen 6. Hatters, 1971
Hmsen I Hatters, 1971
Hansen i Matters, 1971
Hansen i Hitters, 1971
Hansen & Hitters, 1971
thnsen & Hitters, 1971
All error terns in this table are standard error of the mean (S.E.)
- 16 -
(Hansen, 1970). Hansen also reported that, for pH values of 1 to 5, 7 to 8
and 12 to 14, polonium exists mainly in dissolved forms, while for pH values
of 6 to 7 and 10 to 11, most of the polonium exists as a colloid. Thus, in
the acidic organic and acidic sandy soils of the Precambrian Shield,
polonium may exist only in the dissolved form*
The recommended K., value means, standard deviations, ranges and
distribution parameters for polonium by soil type, based on Table 8, are
given in Table 9.
TABLE 9
SoilType
Sand
Silt
(mL/g)
504.2
692.5
S.D.
1215
535.7
FOR POLONIUM
n
35
13
K. Range(mL/g)
13 to 7020
24 to 1830
2
2
LognormalDistribution\i a
.188 0.6574
.607 0.5789
Baes and Sharp (1981) suggested a mean value of 2.7 for the
log10K for polonium, with a corresponding standard deviation of 0.3 (see
Table 1). The value for [i is higher, but the range of K., values is
narrower, than recommended for lead.
Polonium References
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Hansen, W.R. 1970. Polonium-210 in soils and plants. Special Report onU.S. Atomic Energy Commission Contract No. AT(11-1)-1733, COO-1733-11.
Hansen, W.R. and R.L. Watters. 1971. Unsupported 210PoO2 in soil: Soiladsorption and characterization of soil solution species. Soil Sci.112, 145-155.
- 17 -
3.7 PLUTONIUM
Plutonium, like americium, has been studied extensively because of
weapons testing in the 1950s. The summary on plutonium geochemistry pre-
sented by Johnston and Gillham (1980) indicates that
(1) Pu4* is considered the most probable oxidation state in the envi-
ronment because of reduction of Pu "*• to pu^* by organic materials;
reduction of Pu4* to P u ^ could occur at pH <6 under anaerobic
conditions;
(2) plutonium adsorption is a function of oxidation state (Pu6*" is
adsorbed less than Pu 1^), organic matter content and solution pH;
(3) K, values for plutonium reported in the literature were often
obtained without knowledge of the oxidation state, and caution
must be used in interpreting results that use these K, values.
Most K, values in the literature apply to aerobic conditions. The recom-
mended K value means, standard deviations, ranges and distribution para-
meters for plutonium by soil type, based on Table 10, are given in Table 11.
TABLE 11
SoilType *4
(mL/g)
S.D.
FOR
n
PLUTONIUM
K^ Range(mL/g)
LognormalDistribution|j 0
Sand 1.041x103 1.568x103 19 33 to 6.865x103 2.663 0.5964
Si l t 1.3871x104 3.0836x104 8 230 to 9.0x104 3.474 0.7906
Clay 4.2842x104 6.8934x104 13 316 to 1.9x10b 3.706 1.047Organic 2.2902xl04 2.8181xl04 4 1.655xlO3 to 6.2X101* 3.970 0.7469
Baes and Sharp (1981) suggested a mean value of 3.3 for the
log10K, for plutonium, with a corresponding standard deviation of 1.0 (see
Type Sind 5Ut Clay
Sand fine sanily loanfine sandy Iranfine sandy loaafine sandy loan
light l alight loan
coarse sand
44.0 20.0 36.064.0 14.0 22.044.0 24.0 32.066.0 11.0? 23.038.0 32.0 30.074.0 12.0 t .074.0 12.0 14.078.0 2.0 20.048.0 34.0? 18.082.0 9.0 9.0
subsoil sandsubsoil sand
Silt sl l ty clay loansl l ty clay loan
loam
loan16.0 50.0 34.09.0 54.9 37.0
31.0 53.0 16.0s i l t suspended In se
Clay clayclayclay
5.0 31.0 64.032.0 32.0 36.032.0 32.0 36.010.0 34.0 56.0
treated day
XOrganic
: , 4
5.75.78.48.4
-
2.43.4
0.20.30.10.30.10 . 7
0.7
0 .6--
2.82.82.52.50.82.33.6
awter0.60.6
-
0.71.02 .7
3.2-
Ct-sat. soil clay fraction
Ca-sat. soil clay fraction
Ca-sat. soil clay fraction
abysaal red clay
abyssal red clay
Organic organicorganic
bone charcoalcoconut charcoal
-
-
40.840.8
--
c*r>3
_------
0.40.37.95.2
0 .0
0 .60.00.2
0.20.7
2 .0
2 .0----
17.20 . 60.7
---
-
2.4
0 .0
0 . 00.9-
-
-
-
-
----
pH«Saturated Taste
5.3 (4.08)5.3 (5.57)5.0 (4.42)5.0 (6.06)6.0 (5.56)6.0 (6.57)
7-S
5.75.68.38 . )7.5
8 .0
8.25.46.4
4.88.6 (6.5)8.6 (9.3)5.9 (5.83)5.9 (6.85)6.7 (6.13)6.7 (6.83)
7.82.33.6-
7.8 (7.29)7.8 (8.28)
7-8
7.94 .85.46.24 . 0
6.5
6.5
6.5
2.7
6.9
7.2 (6.24)7.2 (7.25)
7.07.0
K
F
fV)
-------
0.410.520.430.470.450.430.440.540.490.57------
0.440.570.56----
0.420.490.450.57
-
-
-
_
-
-
---
-
VALUES TOR
(T.Cn»q,100 g)
15151515
1515
-
20.017.513.8
8.217.5
6.45.82.97.0
3.85.05.0
2020
2525
15.516.217.4
-3030-
29.620.516.034.4
-
-
-
_
-
60
60-
-
TABLE 10
FLL1OK1LW :
Z Free
Iron Oxides
1.651.651.521.525.29
5.29-
_
-----------
1.291.292.412.41
--
--
1.201.20-
-----
-
-
_
-
1.571.57--
LTERAIWE SURVEY SuMIAiQ'
CarpetingCation
-
-----
Na (907. sa t .solution)
----------------_----
Na (9Ot sa t .solution)
----
5 azaol/L Ca^"(Ca N0,)2
5 nmol/L C a *
(Ca N0q)25 nmol/L Ca^*"
(Ca N0,)2
5 umol/L Ca*(Cracetate)0.68 mnol/LNaCl0.691 NoCl
solution---
-
(mJg)
8.5xlO2
1.515x10*9 . J 8 X 1 0 '3.3x10'6.85xlO3**1.352xlO3
2xlO2
2.2xl03 ± 460+2.OxlO2 ± 24+3.2xlO2 1 26+6.9xlO2 ± 110+2.1xlO3 ± 640+l.OxlO2 ± 7+4.3xl02 i 27+2.8xlO2 ± 5+l.OxlO2 ± 5+8.0x10' t 3+Ul4xlO3
2.OxlO2
6.3O2xlO3
3.024xl03
4.938xl03
4.341xl03
1.7xlO3 t 70+4.3xlO2 ± 23+2.3X1O2 1 10+9x10"7.44xlO2
3.61X1O2
lxlO"
1.9xlO3 ± 110+2.6xl03 t 640+8.lxlO2 t 130+7.1xl02 ± 36+1.9xlO5
1.04xlOs
1.63xl05
7.5x10"
3.16xl02
2.5X1O3
2.951xlO3
1.655xl03
6.2x10"2.5x10"
Soil Locationor [description
Milbla (Louisiana)felbls (Louisiana)Lyaun (ttilne)Lyman (telne)Alken (California)Alken (California)(Netherlands)
Colorado A (Rocky flats)Colorado B (Sugar Loaf)Idaho BIdaho CIdaho DWashington A (Hanford)Vbshlngton B (Ifenford)S. Carolina (&n*«n)New *-xlco (Los Alms)Arkansas BhanfordHanfordSiarpsburg (Iowa)Sharrsburg (Ioua)Yolo (California)Yolo (California)Idaho AArkansas CIllinois
tbltsvlllett>ltsville(Netherlands)
Colorado C (Rocky Plats)Ifennessee (Oak Ridge)Neu York (West Valley)Arkansas A2MJ"u(VI)
237Pu(IV)
23sPu(W)
235pu(VI)
—
EgbertEgbert—
—
Reference
Nlshita et a l . ,Nlshita et a l . ,Nlshita et a l . .Nlshlta et a l . .NisMta et a l . .Nlshlta et a l . ,
197919791979197919791979
Hamtra & Verkerk, 197 7
Glover et a l . ,Glover et a l - ,Glover et a l . ,Glnver et a l . .Glover et a l . ,Glover et a l . ,Glover et a l . ,Glover et a l . ,Glover et a l . ,Glover et a l . ,Bcdes, 1957modes, 1957Mshlr* et al.Nlshiu et al.NisMu et al.,NLshita et a l .Glover et a l . ,Glover et a l . ,Glover et a l . ,PUlal & HithnvKlshlta et al.Wshlta et a l .
1976197619761976197619761976197619761976
1979197919791979
197619761976, 19/5
19791979
ihimtni t Verkerk, 1977
Glover et &1.,Glover et a l . ,Glover e t a l . ,Glover et a l . ,
1976197619761976
Bondietti & Reynolds,1976
Boodlettl et a l . , 1975
Bondietti et a l . , 1975
Bondietti et a l . , 1975
Eridtsor.. 1980
Erlckson, 1980
KLshiU et a l .Nlshlta et a l .Taura, 1972Tamira, 1972
, 1979, 1979
Wien the value is bracketed, It Is pH of the extract.
Nlshlta et a l . , 1978 report Plutonian KJ values w.r.t. pH for this soil.d
K, value determined with Initial plutonlun concentration of 10~s mol/L (data foa
Sind, s i l t aivi clay percentages exceeded 1002 in original report.
OO
I
10~7 and 10~6 mol/L can he found In the reference).
- 19 -
Table 1). Allard et al. (1977) reported that the plutonium K, range for
both granite and clay/mud Is 6.3 x 10 1 to 1.6 x 10 2 mL/g. Vandergraaf
(1982) recommended a K, valia
2.0 x 103 mL/g for granite.
(1982) recommended a K, value range for plutonium of 2.8 x 10 2 to
Plutonium References
Allard, B., H. Klpatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and rock. Part 1. Determination of distributioncoefficients. KBS Technical Report 55.
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Rep' ft, CONF-810606-44.
Bondietti, E.A. and S.A. Reynolds. 1976. Field and laboratory observationson plutonium oxidation states. In: Proceedings of the Actinide-Sedi-raent Reactions Working meeting at Seattle, Washington, 1976 February10-11, 1976, Battelle Pacific Northwest Laboratories Report, BNWL-2117,pp. 505-537.
Bondietti, E.A. S.A. Reynolds and M.H. Shanks. 1975. Interaction of pluto-nium with complexing substances in soils and natur.il waters. In;Transuranium Nuclides in the Environment. International Atomic EnergyAgency Report, IAEA-SM-199/51, pp. 273-287.
Erickson, K.L. 1980. Radionuclide sorption studies on abyssal red clays.In: Scientific Basis of Nuclear Waste Management Vol. 2. Plenum Press,ed. C.J.M. Northrup.
Glover, P.A., F.J. Miner and W.0. Polzer. 1976. Plutonium and araericiumbehaviour in the soil/water environment. I. Sorption of plutonium andamericium by soils. _Iti: Proceedings of the Actinide-Sediment Reac-tions Working Meeting at Seattle, Washington on 1976 Feb. 10-11. Bat-telle Pacific Northwest Laboratories Report, BNWL-2117, pp. 225-254.
Hamstra, J. and B. Verkerk. 1977. Review of Netherlands program for geo-logic disposal of radioactive waste, ^n: Nuclear Power and its FuelCycle. International Atomic Energy Agency Report, IAEA-CN-36/289.
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Nishita, H., A. Wallace, E.M. Romney and R.K. Schulz. 1979. Effect of soiltype on the extractability of 237Np, 239Pu, 241Am and 244Cm as a func-tion of pH. NUREG/CR-0997 UCLA 12-1192. 32 pp.
- 20 -
Pillai, K.C. and E. Mathew. 1975. Plutonium in the aquatic environment -its behaviour, distribution and significance, la: Transuranium Nucli-des in the Environment. International Atomic Energy Agency Report,IAEA-SM-199/27.
Rhodes, D.W. 1957. The effect of pH on the uptake of radioactive isotopesfrom solution by a soil. Soil Sci. Amer. Proc. 1_, 389-392.
Taraura, T. 1972. Sorption phenomena significant in radioactive waste dis-posal. J n: Underground Waste Management and Environmental Implica-tions. Amer. Assoc. Pet. Geol. Mem. l&j 318-330.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
3.8 PROTACTINIUM
Nothing on K, values or soil chemistry for protactinium was found
in the literature. We suggest that K values for thorium or uranium bed
used, or even some combination of the values for these elements, such as
|(Th+U).
3.9 RADIUM
The interaction of radium with geological materials and soils, and
the environmental behaviour of radium have been documented by Gillham et al.
(1981b); Nathwanl and Phillips (1979), and Sheppard (1980), respectively.
The K values for radium vary from 50 to 1000 tnL/g (Gillham et al., 1981).d
Johnston and Gillham (1980) summarized the information relevant to K asd
follows:
(1) Radium is present as Ra in the pH range 4 to 8, and does not
readily form complex species.
(2) Radium can be expected to coprecipitate with BaSO4, carbonates and
ferric hydroxides.
(3) Cation exchange is an important adsorption mechanism, since K,
values have been correlated to cation exchange capacity (CEC).
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario K0J 1J0.
- 21 -
The recommended K value means, standard deviations, ranges andd
distribution parameters for radium by soil type, based on Table 12, are
given in Table 13.
TABLE 13
FOR RADIUM
SoilType 4
(mL/g)
S.D. ^ Range(mL/g)
LognormalDistributionu a
Sand
Silt
Clay
1
3
1
.0435x104
.0x105
.5637x104
2
41
.0845x10
.3566x10
.7216x10
4
5
4
3
48
106 to 3.8x104
2.0x104 to 9.5x105
696 to 5.6x104
3.402 1.289
5.10 0.6362
3.961 0.5522
The K, values for strontium may be used as a guide because of the
chemical similarity of radium and strontium. Baes and Sharp (1981)
suggested a mean value of 1.4 for the log1QK for strontium, with a corre-
sponding standard deviation of 0.9 (see Table 1). Allard et al. (1977)
reported a K, range for radium of 40 to 79 mL/g for clay/mud and 63 to
100 mL/g for granite. Vandergraaf (1982) recommended a K range of 5 tod
5000 mL/g for granite. Since no data were found for organic soils, theradium K.value for clay, or the strontium K. value for organic soil, is
d arecommended.
Radium References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Adsorption of long-livedradionuclides in clay and bedrock. Part 1. Determination of distribu-tion coefficients. KBS Technical Report 55.
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Cochran, J.K. and S. Krishnaswami. 1980. Radium, thorium, uranium and21°Pb in deep-sea sediments and sediment pore waters from the northequatorial Pacific. Amer. J. Sci. 280, 849-889.
S a i l X % X 7. %Type Sire] Silt Clay Orgsnlc CaJD3 Saturai
pH E. CECted Pas t e (V) (roeqAOO g)
Z free CbopetingI ron Oxides Cation
Soil locationor Description Btference
SanJ 93.0 5.0 2.0 0.05 40.8 7.8 (Cad2)
Silt
Oay.
91.1
91.1
35.0
6.7
6.7
43.7
43.7
31.0
6.8
6.8
36.0
47.9
47.9
48.9
4S.9
34.0
I . I
1.3
29.0
45.4
45.4
7.4
7.4
35.0
3.1
3.1
0.41
16.2
16.2
1.0
1.0
0.81
5.2
5.2
33.8 8.5 (Caa2)
5.4
5.4
4.3
4.3
5.2 7.8 (Can,)
clay
clay sedliiEnt
day sedtnent
clay sedL-mt
clay sedtnEnt
clay sediitent
clay sedbicnt
7.55?
10.9
10.9
8.32
34.7
34.7
10,4
10.4
31.48
Initial Racone, beforesoil contact1.6xlCT5 mg/La24" 0.05 mlA
no Ca
Initial Racone, beforesoil contact4xlCT5 og/LCaM 0.05 HDIA
no Ca
Ca2*" 0.05 nol/L
no Ca
Initial Racone, beforesoil contact3.7xlO-5 mg/LNi+288 mg/LCa21" 75 mg/L
-
-
-
-
-
106 ±16
4x10 3
3.8X1011
1262 ± 370
l . lxlO 5
9.5xl05
l.OtlO"
1.2xl05
696 ± 185
S.fodO1*
13.3X103*
lO.SxlO3*
8.OslO3*
4.3X1O3*
14.9X103*
17.4X1O5*
Learalngton (6)nedlun sand
St. Trams
St. Ihanns
WRBf(2) d a y loam
Uendover
Vfendover
GrlJDBby
Grtasby
Alberta clay losa
d a y , nud
d a y sediment (Pacific)
clay sediment (Radf lc)
clay sedloent (Pacific)
clay sediment (Pacific)
clay sedliEnt (Pacific)
c lay sediment (Pacific)
Clllhan e t a l . , 1981b
Nathvanl 4 Ph i l l i p s ,1979
Nathwni & n j l l l p s ,1979
Clllhamet a l . , 1981b
Nath«nl 6 P h i l l i p s ,
1979fethumi & R i i l l l p e ,
1979N3thuml 5 Ph i l l i p s ,
1979fethuml 5 Phil l ips ,
1979Gt l lhmet a l . , 1981b
Allard et a l . , 1977
Cochrai & Krlshnaswmn.1980
Cbchran & KrlshnasuamlI960
Cbchran & KrLshnaswaBl1980
Cbchran & Krlshnaswnl1990
Cbchran & Krlshnasvonl1980
Cbchrsn & KrlAhnastHsl1980
1WE - Ihlteshell Mclear tewarch &£abllsta-nt, Plnaw, Mmltota
Minimni values reported and data based on desorptlon of deep sea clays.
IsJ
- 23 -
Gillham, R.W., H.D. Sharma, M.R. Reddy, E.L. Cooper and J.A. Cherry. 1981b.Barium and radium migration in unconsolidated Canadian geological mate-rials. Atomic Energy Control Board Report, INFO-0048.
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR--90*.
Nathwani, J.S. and C.R. Phillips. 1979. Adsorption of 226Ra by soils inthe presence of calcium (2+) ions. Specific adsorption (II). Chem-osphere 8 293-299.
Sheppard, M.I. 1980. The environmental behaviour of radium. Atomic Energyof Canada Limited Report, AECL-6796.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
3.10 THORIUM
Little information is available in the literature on thorium in-
teractions in the environment; however, two brief reviews of thorium chemis-
try are available (Rancon, 1973; Sheppard, 1980). Johnston and Gillham
(1980) summarized the information relevant to K as follows:
(1) The primary thorium adsorption mechanism is ion exchange.
(2) In non-calcareous soils, thorium adsorption is extremely sensitive
to initial thorium solution concentrations. In organic materials,
increased pH causes increased humic acid solubility and thorium
complexation, resulting in lower K values. In calcareous soils,d
K values are high (> 10 mL/g), regardless of pH or thorium con-
centration, because of the buffering capacity of the soil and the
precipitation of Th(0H)4<
(3) K., values are generally high, (> 103 mL/g), in dilute solutions,
indicating limited thorium migration.
The recommended K value means, standard deviations, ranges and distribu-d
tion parameters for thorium by soil type, based on Table 14, are given in
Table 15.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
TABLE 14
, VALUES FOR THORIUM : LITERATURE SURVEY SUtHARY
Soil 7, % Z 7, 7, pH E. CECType Sand Silt Clay Organic C3CO3 Saturated Paste (V) (meq/100 g) I
7. Free Competingran Oxides Cation
Soil Locationor Description Reference
Sand 45 <XS1O,)40 (7-
40 (Z
Organic 5 (X
5 a
30
60
60
12
12
0
0
60
60
25 C. car-bonate)
0 (Z car-bonate)
0 (% car-bonate)
23 (7, car-bonate)
23 (2 car-bonate)
7.0
3.2
4.8
6.7
7.4
Th Cone. 1.5xl05 Cadarache sediment tencon, 1973(1 g/L)Th Cone. 8 clay schist Bancon, 1973(1 g/L)Th Cone. lx lO 5 c l ay sch i s t Rancon, 1973(0 .1 g/L)Th Cone. 8x10'* rt\<er peat tencon, 1973
(lgA.)Th Cone. 1.5x10* river peat(0.1 g/L)
Rancon, 1973
- 25 -
SoilType
Clay
Organic
(mL/g)
5.0x10 **
4.75xlO474
S.D.
.0710x104
.5962x104
TABLE
FOR
n
CSI
CM
15
THORIUM
K^ Range(mL/g)
8.0 to 1.0x105
l.SxlO'' to 8.0x10 h2
4
LognormalDistribution
.95 2.90
.54 0.5141
Baes and Sharp (1981) suggested a mean value of 4.8 for the
log^QK, for thorium, with a corresponding standard deviation of 0.6 (see
Table 1). Allard et ai. (1977) reported K ranges from 40 to 316 mL/g andd
500 to 1260 mL/g for clay/mud and granite, respectively. Vandergraaf (1982)
recommended a K value for thorium of 850 mL/g for granite.
Thorium References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and rock. Part 1. Determination of DistributionCoefficients. KBS Technical Report 55.
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Johnston, H.M. and R.W. Glllham. 1980. A review of selected radlonuclldedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Ran^on, D. 1973. The behaviour in underground environments of uranium andthorium discharged by the nuclear industry. In: Environmental Behav-iour of Radionuclides Released in the Nuclear Industry. InternationalAtomic Energy Agency Report, IAEA-SM-172/55.
Sheppard, M.I. 1980. The environmental behaviour of uranium and thorium.Atomic Energy of Canada Limited Report, AECL-6795.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario K0J 1J0.
- 26 -
3.11 URANIUM
Several reviews of uranium chemistry exist (Harmsen and de Haan,
1980; Borovec, 1981; Sheppard, 1980), but few K values have been reported
in the literature. The summary on uranium geochemistry presented by John-
ston and Gillham (1980) indicates that
(1) in oxidizing environments, U ***" compounds are stable and can pre-
cipitate, whereas U4* is stable in a reducing environment and
would precipitate as U02; thus the oxidation-reduction status is
important;
(2) soluble uranium (U6*) can be adsorbed or reduced by organic mat-
ter; if U6"1" is reduced to U4"1", precipitation can occur;
(3) UC^2* can be adsorbed by clay minerals by cation exchange, but may
also form complexes with anions such as carbonate or phosphate.
Borovec (1981) indicated that K, values for uranium for clay minerals range
from 50 to 1000 mL/g and for peat from 10 4 to 106 mL/g. The recommended
K, value means, standard deviations, ranges and distribution parameters for
uranium by soil type, based on Table 16, are given in Table 17.
SoilType
Sand
Clay
8
2
(mL?g)
.065
.6349x10511
4.
*d
S.D.
.22
5597x10
TABLE
FOR
n
25 3
17
URANIUM
KJ Range(mL/g)
0.13 to 16.0
200 to 7.9x105
LognormalDistribution
u a
0
3
.159 1.478
.543 2.040
Baes and Sharp (1981) suggested a mean value of 1.6 for the
log1QK for uranium, with a corresponding standard deviation of 0.6 (see
TABLE 16
K. VALUES FOR URANIUM : LITERATURE SURVEY SUrMAKY
SoU I * Z X * pM« E^ <SC * FreeType Sand Silt Clay Organic CaCX)3 Saturated Paste (meq/lQO g) Iron Oxides Catlcn (Jg)
Soil locationor Description
Sand
SiltOjy.
Organic
45 -; sioj)
30
sandy soilalluvial i
40; SID2)
abyssal redabyssal red
5
: sin,)
soil60
cLsvclay
12
< 1
--0
-60
25 OS car-bonate)
--
0 (Z car-bonate)
--
23 (7. car-bonate)
<
i
2.7,
7
7
.8
.17
Cadarache seduisnt I^ncon» 1973
4.3 ug CD^/wL 0.134.3 ug tT3
2-/nL 0.25270 altered schist
0.68 rolA NaCI 2000.68 m l A Nad 7.9J1O5 - -
33 organic pest
Yataicto et a l . , 1973Yanancto et a l - . 1973Rancon, 1973
Erickson, 1980Erlckson, 1980Rancon, 1973
Iro
- 28 -
Table 1). Allard et al. (1977) reported K, ranges from 2.5 to 20 mL/g ford
clay/mud and 4 to 13 mL/g for granites. Vandergraaf (1982) recommended a Kd
range of 0.4 to 10 mL/g for granites.
Uranium References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and rock. Part 1. Determination of DistributionCoefficients. KBS Technical Report 55.
Baes H I , C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Borovec, Z. 1981. The adsorption of uranyl species by fine clay. Chem.Geol. 32_, 45-48.
Erickson, K.L. 1980. Radionuclide sorption studies on abyssal red clays.In: Scientific Basis of Nuclear Waste Management Vol. 2. Plenum Press,ed. C.J.M. Northrup.
Harmsen, K. and F.A.M. de Haan. 1980. Occurrence and behaviour of uraniumand thorium in soil and water. Neth. J. Agric. Sci. 8_, 40-62.
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Ran$on, D. 1973. The behaviour in underground environments of uranium andthorium discharged by the nuclear industry. _In: Environmental Behav-iour of Radlonuclides Released in the Nuclear Industry. InternationalAtomic Energy Agency Report, IAEA-SM-172/55.
Sheppard, M.I. 1980. The environmental behaviour of uranium and thorium.Atomic Energy of Canada Limited Report, AECL-6795.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Yamaraoto, T., E. Yunoki, M. Yamakawa and M. Shimizu. 1973. Studies onenvironmental contamination by uranium. 3: The effects of carbonateIon on uranium adsorption to and desorption from soils. J. Radiat.Res. 14_, 219.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
- 29 -
4. DISTRIBUTION COEFFICIENTS FOR FISSION PRODUCTS
4.1 CALCIUM
K, values for calcium reported by Graham (1973) and Graham and
Silva (1979) vary from 1 x 10-3 to 9.8 mL/g; however, there is some
confusion about the units. Wong et al. (1983) reported K values of 1117
and 1900 mL/g for a sand and a muck soil, respectively. It is recommended
that the K values for strontium be used for calcium (see Section 4.11).
Calcium References
Graham, E.R. 1973. Selective distribution and labile pools of micronutri-ent elements as factors affecting plant uptake. Soil Sci. Soc. A'Jier.Proc. 37_, 70-74.
Graham, E.R. and C.G. Silva. 1979. Labile pools and distribution coeffi-cients for soil calcium, magnesium, and potassium determined with ox-change equilibria and radioisotopes. Soil Science 128, 17-22.
Wong, K.V., S. Sengupta, D. Dasgupta, E.L. Daly, Jr., N. Nemerow and H.P.Gerrish. 1983. Heavy metal migration in soil-leachate systems. Bio-cycle 24, 30-33.
4.2 CARBON
Allard et al. (1981) studied the sorption of Hi£*C0 ~ on some
solids using the batch technique. The sorption of 14C was generally low,
but appeared to increase with increasing calcium content of the solid.
Retardation factors of up to 3 (i.e., three times slower transport of i4C
than of water) were measured for calcite. Concrete will probably retain
most of the 14C, and a retardation factor >10 might be expected for a
bentonite-quartz mixture (K, = 2.2 x 10"6 mL/g). Owing to the paucity of
information, a conservative retardation factor of 1, or a K of 0 mL/g, is
recommended.
- 30 -
Carbon Reference
Allard, B., B. Torstenfelt and K. Andersson. 1981. Sorption behaviour of1L|C in groundwater/rock and in groundwater/concrete environments.Report Prav 4.27.
4.3 CESIUM
The work of Gillham et al. (1981a) is the most extensive on K.
values for cesium for Canadian soils. Their study showed that for 15 Cana-
dian soils, K values for cesium ranged from 1 x 10 2 to 2 x 10 4 mL/g, but
there was no significant correlation between the K value and measured soild
properties such as CEC, major cation concentration, clay mineral composi-
tion, organic matter content and pH. In more than half of the samples, how-
ever, the K values were related significantly to the natural exchangeable
cesium content of the soil, and this must be accounted for in sorption
studies.
The recommended K value means, standard deviations, ranges and
distribution parameters for cesium, based on Table 18, are given in Table
19.
SoilType
SandSiltClay
21631.1395xlO4
8379
K
S.D.
322678991.3613X101*
TABLE
_, FOR
n
24205
19
CESIU1
1065065
•1
K, Range(mL/g)
tototo
l.OxlO4
3.0x10h
3.15x10 *•
232
LognormalDistributionM- ^
.668 0.9332
.912 0.4227
.945 1.216
Baes and Sharp (1981) suggested a mean value of 3.0 for the
log1QK for cesium, with a corresponding standard deviation of 0.8 (see
Table 1). Allard et al. (1977) reported K ranges from 6 to 32 mL/g and 32
TABLE 18
SoUType
Sand
Silt
Clay
7.
Sari)
100
93%5259
6252
%6087-
94
Z
Silt
-
54
4524
3139
2229-
I
Clay '
-203
17792
184-
6 (<O.O74 ma)river sand
subsoil randclinoptilollte
84
63
363428123445
BurbankBurhankBurtn*ftn-nanV
13
32
sardsandsand353541553444
soilsoilsoilsoil
3
5
293111333211
alluvial silt loam• i
313818403445
7183
tedlun lnam69626645
5247927196
sUtv clay.sil ty clay44
315034
00
16151481
111
, f>*-3, PC-2
635
10&T < 0.02 mn
-lay
Savannah River serf.Savannah River sed.
-
0.05O.i".O.'«0~0o.y0.330.302.050.10
---
-
-----
0.16
0.21
---
0.430.401 .270.350.850.14(Ap)---
-----
----
0.230J31-
JOC03 Saturated Paste (V)
41.340.8000
18.343.411.17.10.07---
2-----
2.8
1.36
---
33.634.1
21.105.11.4-------------
3.85.2-
-
(<100 urn) -(<100 urn) -
8.3 (C«C12)7.8 (CaCl2)6.3 (Cad2)5.0 (CaCl,)6.5 (CaT.l2)7.6 (C*C12>8.0 (Cad2)8.0 (CaCl2)7.8 (Cad2)8.23 (CaCl2)
--
7-8
8.6------
-
7.07.07.0
8.1 (Cad2)8.1 (CaCl2)
6.7 (CaCl2)7.7 (Cad2)B.83 (CaCl2)
--------------
7.8 (Cad2)-
7-8
-7.0
K VALUES FOR CESIUM : LTBKAWRE SURVEY S
C£C 1 Free Coveting(meq/100 g) Iron Oxides Cation
1.41.21.11.61.92.20.70.4
21.25.0---
5-----
5.1
5.3
---
8.48.65.9
10.232.712.0
--2.62.76.31.84.91.54.23.55.2--
11.031.535
-
--
R«? ref.see ref.see ref.see ref.see ref.see ref.see ref.see ref-see ref.see ref.
so;
90S NaClsolution4 TOI/L NaCl
-grouncHoter3 HDI/L NaNO3
0.5 raol/L NJCI0.25 ITOI/L Ci£l2
0.63 0.2 nol/L Nadsee ref.
1.02 0.2 nclA Nadsee ref.
---- see ref*
see ref-
see ref.sec ref.
-0.1 nul/L W0,
-_--_-__--
1.21 0.2 tml/L NaClsee n-f.
- -
9CK NaClsolution
Nad_
V
(ot/8)
1.19x10^1.37x103
7.4X101
1.0x10"l.OxlO3
1.0x10"1.5xl02
5.OxlO2
l.OxlO2
1.5xlO3 ±189.5xlO?
10
16.44.2xlO3
9.OxlO3
4.66X102
1.09xl03
5.21xlO3
2.4OX1O3
3.51xlO3
98*84*40*1.78x10"1.84x10"
2.0x10"
l.OxlO1'1.35x10"3x10"6.5xlO2
5J2xlO 3
9.55xlO3
1.04x10"1.14x10"
7.3xlO3
6.2xlO3
2.07x10"1.52X1O11
2.0x10"3.OxlO3
2.7xlO3
3.96x103
1.0x10"3.15x10"
2x102
65 (n-8)130*
Soil Location
or Description
Soil *4 (IKRE)Soil ' 6 (Leamington)Soil HI (C1M.)+
Soil «8 (North Bay)Soil »10 (VNRF.)
Soi l #11 (WRE)SoU #12 ( a m ) *
Soil « 3 (C.F.B. Borden)SoU « 6 (Alberta)
320 Sediiuent B (Solution 1)
Iron & s i l t y sandsConposite s o i l
River sand
Hanford BubsoU
CUnopt i loUte (Idaho)Burbark soUBurbank so i lBurba* so i lBurhank so i l
Burhank sand (average profi le)
Ephrata sard (average profUe)
Four ndle creekPen BranchPar Pond
SoU »1 (1«RE)Soil n (KIRE)
SoU #5 (Leamington)Soil M (North Bay)SoU »14 (Alberta)
± 4741 Sediioent A (Solution 1)Captlna s i l t loan (Ap)SodpodzoUc s o i l
a l l uv ia l soU (Cadarache)a l i n r i a l soU (Cadarache)Vlndobonian sed. (Cadarache)
Vlndobonlan sed. (Cadarache)Vlndobonian sed. (Cadarache)Vindobooian sed. (Cadarache)
sandy-day sed. (Durance R.)sandy-clay sed. (Durance R.)
sandy-day sed. (Durance R.)s l l ty clay (Idaho)s l l ty clay (Idaho)Ritzvllle s i l t (avg. profile)SoU '15 (Alberta)very fine suspended sediments
(Durance River)clay
Savannah River sedLaentsSavannah River clay
Reference
Glllham et a l . , 1981aGlUham et a l . , 1981aCUlhan et a l . , 1981aGUlham et a l . , 1981aGlllham et a l . , 1981aGlllham et a'.., 1981aClllhan et a l . , 1981aGUlham et a l . , 1981aGlllham et a l . , 1981aSeme et a l . , 1978Tyrochowlcz, 1981SchmLt, 1972Harotra S Verkerk, 1977
BrxJes, 1957Wlldung 4 Rhodes, 1963Hajek 4 Aoes, 1968Hajek 4 ABES, 1968Hajek 4 Aces, 1968Hajek S, Area, 1968RoutBon, 1973
Rcutaon, 1973
Zelazny et a l . , 1978Zelazny et a l . , 1978Zelazny et a l . , 1978GUlham et a l . , 1981aClllhaa et a l . , 198UClllham et a l . , 1981aGlllham et a l . , 1981aGUlhas et a l . , 1981aSeme et a l . , 1978Rogowkl 4 Taoura, 1965Aleksakhln, 1965Rancon, 1972Rancon, 1972Rancpn, 1972Rancon, 1972Rancon, 1972Rancon, 1972Rancrm, 1972Rancon, 1972Rancon, 1972Ulldung I Rhodes, 1963Wlldffi££ & FnoQCSf I763Rutson, 1973Glllhao et a l . , 1981aRancon, 1972
Hanstra 4 Verkerk, 1977
Elprince « a l . , 1977Zelazny et a l . , 1978
CW1L - Chalk River Nuclear Laboratories, Chalk River, Ontario
HFP - Rnre Nuclear Pc*«r Development
AL«w dat^ for sorption versus p?I, see reference.
- 32 -
to 794 mL/g for clay/mud and granite, respectively. Vandergraaf (1982)
recommended a K,range of 40 to 1000 mL/g for granite.
Cesium References
Aleksakhln, R.M. 1965. Radioactive contamination of soils and plants.USAEC Report AEC-tr-6631.
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorptlon of long-lived radio-nuclides in clay and rock. Part 1. Determination of DistributionCoefficients. K.BS Technical Report 55.
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Elprince, A.M., C.I. Rich and D.C. Martens. 1977. Effect of temperatureand hydroxy aluminum interlayers on the adsorption of trace radioactivecesium by sediments near water-cooled nuclear reactors. Water Resour.Res. 13_, 375-380.
Gillham, R.W., L.E. Lindsay, W.D. Reynolds, T.J. Kewen, J.A. Cherry and M.R.Reddy. 1981a. Studies of cesium and strontium migration in unconsoli-dated Canadian geological materials. Atomic Energy Control Board Re-port, INFO-0049.
Hajek, B.F. and L.L. Ames, Jr. 1968. Strontium and cesium equilibriumdistribution coefficients: Batch and column determinations.BNWL-481-3.
Hamstra, J. and Verkerk, B. 1977. Review of Netherlands program for geo-logic disposal of radioactive waste. JLn_: Nuclear Power and its FuelCycle. International Atomic Energy Agency Report, IAEA-CN-36/289.
Rancon, D. 1972. Practical utilization of the distribution coefficient forthe measurement of the radioactive contamination of minerals in rocks,soil and subterranean water. Cadarache Nuclear CEA Research Center,ANL-trans-931, Report-R-4274.
Rhodes, II.W. 1957. The effect of pH on the uptake of radioactive isotopesfrom solution by a soil, boil Sci. Amer. Proc. n_, 389-392.
Rogowski, A.S. and T. Tamura. 1965. Movement of 137Cs by runoff, erosionand infiltration on the alluvial Captina silt loam. Health Phys-11_, 1333-1340.
Routson, R..C. 1973. A review of studies on soil-waste relationships on theHanford Reservation from 1944 to 1967. BNWL-1464, UC-70.
- 33 -
Serne, R.J., D. Rat and S.J. Phillipso 1978. Monitoring and physical char-acterization of unsaturated zone transport: Laboratory analysis. In:Nuclear Waste Management Quarterly Progress Report Oct.-Dec. 1977,Pacific Northwest Laboratory Report, PNL-2377-4, UC-70.
Schmalz, B.L. 1972. Radionuclide distribution in soil mantle of the litho-sphere as a consequence of waste disposal at the National Reactor Test-ing Station, USAEC Report, IDO-10049.
Tymochowicz, S. 1981. Sorptive properties of mineral deposits occurring inPoland. Nukleonika, 26, 595-599.
Wildung, M.W. and D.W. Rhodes. 1963. Removal of radioisotopes from solu-tion by earth materials from eastern Idaho. IDC-14624.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Zelazny, L.W., D.C. Martens, A.M. El-Prince and C.I. Rich. 1978. Effect oftemperature and hydroxy-aluminum interlayers on cesium selectivity andfixation in river suspensions and soils. ORO-4851-2.
4.4 IODINE
The most extensive study of iodine adsorption on soil was that of
Wildung et al. (1974). Johnston and Gillham (1980) have summarized the
known soil chemistry of iodine as follows:
(1) the most stable form of iodine in both oxidizing and reducing
environments is iodide, I~. Because the predominant iodine spe-
cies is an anion, ion exchange would not be important in soil
adsorption, particularly at neutral or high pH values.
(2) organic matter appears to be a significant factor in iodine ad-
sorption.
(3) K, values for iodine range from 0.1 to 50 mL/g, depending on the
form of the iodine and the pH of the solution. The maximum Kd
value would be obtained for I~ at a pH of 4 to 6.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
- 34 -
Since no K, values for specific soils were found in the literature, thed
multiple-regression equations (based on iodide (I~) and methyl iodide (CH3I)
interactions with 22 soils) reported by Wildung et al. (1974) were applied
to soils already described in this report. The K, values were calculatedd
only for soils whose properties were within the range of the soils used togenerate the multiple-regression equations. The equations for iodide K, and
dmethyl iodide K, differ, and are
d
K. = 0.33 X, + 0.09 X, (5)diodide l 3
K, ,_ , = 0.027 X,, + 0.10 Xo (6)d methyl 2 3
iodide
where X, is the silt content (range for equation development is 17.6 to
58.0%),
X 2 is the clay content (range for equation development is 3.8 to
46.6%), and
X3 is the organic carbon content (range for equation development
is 0.23 to 28.8%).
The recommended K. value means, standard deviations, ranges and distribu-d
tion parameters by soil type (using Equation (6) since it will predict the
lowest K, values because methyl i
Table 20, are given in Table 21.
lowest K, values because methyl iodide is more highly mobile), based on
TABLE 21
K, FOR IODINE—q
Soil KJ S.D. n KJ Range LognormalType (nL/g) OnL/g) Distribution
\i a
Sand 0.5514 0.3595 7 0.2 to 1.210 -0.3404 0.2929Silt 0.9145 0.3201 11 0.18 to 1.50 -7.99xlO~2 0.2351Clay 1.293 0.3697 4 1.03 to 1.83 9.952x10"2 0.1140
- 35 -
TABLE 2 0
K VALUES FOR l O D D E : LITERATURE SURVEY SUMMARY-d •
CalculatedS o i l X X X K .Type Silt Clay Organic (mL/g)
Soil Locationor Description
Reference
Sand
Silt
Clay
31392229392820505453353635415534
5034323234
79185
.4 18
.4 22
.0 3634371625293131333229
635363656
.8
.0
.4
.0
.1
0.38
0.332.050.450.600.982.40.82.33.60.430.410.401.270.350.857.1
0.230.81
1.02.73.2
0.0.0.0.0.0.1.1.1.0.0.0.0.0.0.0.1.
0.1.1.1.1.
2328692055702100237983828896939450
1803072483
Soil lll\ (WNRE)
Soil 012 (BNPD)Soil #16 (Alberta)Hanford AIdaho AIdaho DColorado A
Idaho A
Arkansas CIllinoisSoil Itl (WNRE)Soil 112 (WNRE)Soil 113 (WNRE)Soil 115 (Lemlngton)Soil 119 (North Bay)Soil 014 (Alberta)Brookston stlt(average profile)Ritzvllle siltSoil #15 (Alberta)Tennessee (Oak Ridge)New York (West Valley)Arkansas A
Cillham et al., 1981aClllham et al., 1981aCillham et al., 1981aAmes & Ral, 1978Ames & Ral, 1978Glover et al., 1976Glover et al., 1976Glover et al., 1976Glover et al., 1976Glover et al., 1976Gillhara et al., 1981aGillham et al., 1981aGlllhara et al., 1981aGill ham et al., 1981aGillham et al., 1981aGillham et al., 1981aJuo & Barber, 1970
Routson, 1973Gillham et al., 1981aGlover et al., 1976Glover et al., 1976Glover et al., 1976
The K, range reported for methyl iodide in soil was 0.1 to 3.1
(Wildung et al., 1974). The multiple-regression equations were developed
for mineral soils. A single value of > 30 mL/g for charcoal is pertinent to
organic soil (Novak, 1981). Vandergraaf (1982) recommended a K, value for
iodine of 0 mL/g, until a cationlc species of iodine is identified.
Iodine References
Ames, L-L. and D. Rai. 1978. Radionuclide interactions with soil and rockmedia, Volume 1. U.S. Environmental Protection Agency Report, EPA520/6-78-007.
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Juo, A.S.R. and S.A. Barker. 1970. The retention of strontium by soils asinfluenced by pH, organic matter and saturation cations. Soil Sci.109, 143-U8.
- 36 -
Gillham, R.W., L.E. Lindsay, W.D. Reynolds, T.J. Kewen, J.A. Cherry andM.R. Reddy. 1981a. Studies of cesium and strontium migration in un-consolidated Canadian geological materials. Atomic Energy ControlBoard Report, INFO-0049.
Glover, P.A., F.J. Miner and W.O. Polzer. 1976. Plutonium and aaiericiumbehaviour in the soil/water environment. I. Sorption of plutonium andamericium by soils. In: Proceedings of the Actinide-Sediment Reac-tions Working Meeting at Seattle, Washington on 1976 Feb. 10-11. Bat-telle Pacific Northwest Laboratories Report, BNWL-2117, pp. 225-254.
Nowak, E.J. 1981. Composite backfill materials for radioactive waste iso-lation by deep burial in salt. Scientific Basis of Nuclear Waste Man-agement 2. 545-552.
Routson, R.C. 1973. A review of studies on soil-waste relationships on theHanford Reservation from 1944 to 1967. Battelle Pacific NorthwestLaboratories Report, BNWL-1464, UC-70.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Wildung, R.E., R.C. Routson, R.J. Serne and T.R. Garland. 1974. Pertech-netate, iodide, and methyl iodide retention by surface soils. BNWL-SA-5195.
4.5 MOLYBDENUM
No data were found in the literature for molybdenum; however,
E its position in t
can be used for molybdenum.
because of its position in the Periodic Table, the K. values for technetiumd
4.6 NICKEL
Little information exists for soil adsorption of nickel. Swanson
(1981) reported a range of K, values for nickel of 5.2 x 10 1 tod
1.2 x 104 mL/g for a selected size fraction of Hanford soil (75 to 150 JJU)
with a soil-to-solution ratio of 0.010 g/mL. Contradictory results and the
use of organic complexants in the Swanson experiments indicate that values
for specific samples should not be used.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario K0J 1J0.
- 37 -
Gerritse et al. (1982) suggested that the K, value range ford
nickel is 1 x 10 2 to 1 x 103 inL/g. They reported two sandy mineral soil
values of 6 x 10 * and 3.4 x 10 2 mL/g and four peat soil values of 3.6 x 10 2,
6 x 102, 9.9 x 10 2 and 4.7 x 10 3 mL/g. Wong et al. (1983) reported K
values of 604 and 1437 tnL/g for a saftd and a muck soil, respectively. The
recommended values of \i and a for the K, distribution for nickel, based ond
this information and distribution information for the other nuclides, are
given in Table 22.TABLE 22
RECOMMENDED VALUES OF n AND o FOR NICKEL
Soil Lognorraal DistributionType (i a
SandSiltClay
Organic
1.52.03.03.0
1.0• 1 . 0
1.01.0
Nickel References
Gerritse, R.G., R. Vriesema, J.W. Dalenberg and H.P. De Roos. 1982. Effectof sewage sludge on trace element mobility in soils. J. Environ. Qual.11_, 359-364.
Swanson, J.L. 1981. Effect of organic complexants on the mobility of low-level waste radionuclides in soils: Status report. Pacific NorthwestLaboratory Report, PNL-3927, UC-70.
Wong, K.V., S. Sengupta, D. Dasgupta, E.L. Daly, Jr., N. Nemerow and H.P.Gerrish. 1983. Heavy metal migration in soil-leachate systems. Bio-cycle 24_, 30-33.
4.7 PALLADIUM
No specific information was found on soil adsorption of palladium.
We suggest that the K, values for nickel be used for palladium. Vandergraaf
- 38 -
(1982) reported a range of 0 to 28 mL/g for the K of palladium for granite.d
He recommended that a K value of 11 mL/g be used.d
Palladium Reference
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
4.8 RARE EARTHS - TERBIUM, SAMARIUM AND CERIUM
Terbium, samarium and cerium are fission products, and it is con-
venient to discuss these three rare-earth elements together because of their
chemical similarity. Cerium was the only one of these elements for which
data were found. Vandergraaf (1982) reported that the K, value for ceriuma
ranges from 250 to 5000 mL/g, and recommended a value of 1000 mL/g. Allard
et al. (1977) reported a K range for cerium of 100 to 10 000 mL/g for
clay/ mud and 1000 to 1.6 x 104 mL/g for granite. Baes and Sharp (1981)
suggested a mean value of 3.0 for the logigK, for cerium, with a correspon-
ding standard deviation of 0.6, and a K range of 58 to 6000 mL/g (see
Table 1) for all soils. We recommend using the values of Baes and Sharp for
all soil types.
Rare Earths References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and rock. Part 1. Determination of DistributionCoefficients. KBS Technical R.eport 55.
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario K0J 1JO.
- 39 -
4.9 SELENIUM
Elsokkary (1980) reported selenium adsorption for three soils,
which allowed the computation of K. values of 1.6, 2.2 and 2.5 mL/g on a
clay soil and two silty soils, respectively. Frost and Griffin (1977)
reported a K, value of ~ 50 mL/g for HSeO3~ adsorption on calcium-montmoril-
lonite at a pH of 7. Singh et al. (1981) reported K, values ranging from 3d
to 73 mL/g for selenate adsorption on sandy soils. Since insufficient data
are available, we suggest that the values for polonium be used for assess-
ment purposes.
Selenium References
Elsokkary, I.H. 1980. Selenium distribution chemical fractionation andadsorption in some Egyptian alluvial and lacustrine soils. Z. Pflan-zenernaehr. Bodenkd., 143, 74-83.
Frost, R.R. and R.A. Griffin. 1977. Effect of pH on adsorption of arsenicand selenium from landfill leachate by clay minerals. Soil Sci. Soc.Amer. J. 4^, 53-57.
Singh, M., N. Singh and P.S. Relan. 1981. Adsorption and desorption ofselenite and selenate selenium on different soils. Soil Sci. 132,134-141.
4.10 SILVER
Little information exists for soil adsorption of silver and no
specific soil K, values were found. Consequently, it is suggested that in-d
formation for copper be used for silver because of their proximity In the
Periodic Table. Gerritse et al. (1982) suggested that the K. value rangea
for silver is 1 x 103 to 1 x 105 mL/g. They reported K values of 1.6 x 10 2
and 5.6 x 102 mL/g for copper on sandy mineral soil, and K values ofd
4.4 x 103, 1.7 x 104, 2.2 x 10h and 3.3 x 104 mL/g for copper on peaty soil.
Values for copper also ranged from 5.5 x 104 to 1.2 x 105 mL/g for 0 to
0.9 meq Ca^/g dry peat. Wong et al. (1983) reported K, values for copper
of 206 and 197 mL/g for a sand and a muck soil, respectively. The recom-
mended K, distribution parameter values for silver, based on this informa-
d
tion, on the distribution information for the other nuclides and on Table23. are given in Table 24.
, VALUES FOR SILVER : IJTERAUJRE SURVEY SHHAKI
Type Sirai Silt Clay CdX, Saturated Pasted C X Free Competing
(neqAOO g) Iron Oxides Cation Wg)Sol i Locationor Description ftefer-ence
0
20---
----_
3.5
2,5__
__
90>90>9Q
>90
4.5-5.07.5-8.0
£.86.25.07.46.64.5
4 to 56
6.2
22
16-_-
----—
1.6riO2 Soil C5.6xlO2 Soil D
0.1 nDl/L Cad2 2.7 Florida 1 - sand0.1 rol/l &C12 33.00.1 UDIA. CaCt2 28.0
0.1 ml/L CaCl2 2000.1 iml/L CaQ2 333
Gerrttse et a l . , 1982Gerrltse et a l . , 1982Ctahaa, 1973
Florida 2 - Band + organic oatt£r Grahan, 1973Mssourl 23 Grahan, 1973Missouri 24 Grahai, 1973Mssouri 38 Grahan, 1973
4.4xl03 Soil A Gerritse et a l . , 19822.2xlOJ< Peat A Gerritse et a l . , 19821.7x10" Peat B Gerrltse et a l . , 19823.3idO^ Soil B GHirltce et a l . , 1982
O
I
- 41 -
TABLE 24
RECOMMENDED VALUES OF u AND a FOR SILVER
Lognormal DistributionSoil Type |i a n
Sand 1.726 0.9988 4
Silt 2.090 0.5678 3Clay 4.0Organic 4.184 0.3792 4
Silver References
Gerritse, R.G., R. Vriesema, J.W. Dalenberg and H.P. De Roos. 1982. Effectof sewage sludge on trace element mobility in soils. J. Environ. Qual.ll_, 359-364.
Graham, E.R. 1973. Selective distribution and labile pools of raicronutri-ent elements as factors affecting plant uptake. Soil Sci. Soc. Amer.Proc. 3]_, 70-74.
Wong, K.V., S. Sengupta, D. Dasgupta, E-L. Daly, Jr., N. Nemerow and H.P.Gerrish. 1983. Heavy metal migration in soil-leachate systems. Bio-cycle 24, 30-33.
4.11 STRONTIUM
The most extensive report on strontium K, values for Canadian
soils is the work of Gillham et al. (1981a). For 15 Canadian soils, the Kd
values ranged from 2.5 to 1 x 10 2 mL/g. The study also showed that stron-
tium "in some or possibly many circumstances would migrate at velocities
smaller than the groundwater velocity but at velocities which nevertheless
could be significant."
The recommended K, value means, standard deviations, ranges and
distribution parameters for strontium by soil type, based on Table 25, are
given in Table 26.
TABLE 25
SoliType
zSand
ZSilt
7.day Organic
XOCO,J Satura ted Paste
K, VALUES PCR SntCNITLtl :
CEC Z Free(meq/100 g) Iron Oxide
LITERATURE
Competings Cation
SURVEY S*MARY
<"L?g)Soil Locationor Description Inference
1009396525962966087
4524312
229
203
1772
18A
9.030.050.51
o.oe0.40J.380.302.050.10
94 6 (<0.0/« ran) -
subsoil sandsand 20
Burlnnk soilEurha* m i lBurbar* soliBurhenk soil
84 13 3
63 32 5
p i l f e r sandaquifer sandaquifer sandaquifer sandaquifer sandaquifer sand
2.9
41.340.8000
18.311.17.10.07
8.3 (CadJ7.8 (CaCl.,)6.3 (CaCX,)5.0 (CaCl,)6.5 (CaClj)7.6 (CaCl,)8.0 CCad.)7.8 (CaCl,)8.23 ( d
aC l ,Cad ,) -
1.41.2l. l1.61.92.20.4
21.25.0
519.2
-
5.55.55.55.55.55.5
-
-
DM0.420.420.420.420.42
5.1
5.3
0.25-0.90.25-0.90.25-0.90.25-0.90.25-0.90.25-0.9
see ref.see ref.see ref.see ref.see ref.see ref.see ref.see ref.see ref.
-902 Nadsolution4 rol/L Na+,0.01 mol/L PO,,-
3xlCT3 raol/LSra 2
graundwater3 rol/L NaTO3
0.5 ml/L feel3ncl/LNa0A:0.2 m l A NaClsee ref.0.2 ml/L teasee ref.see ref.*see ref.*see ref.*see ref.*see ref.*see ref.»see ref*
2.0x10'2.52.0xi0'l.OxlO2
2.5x10'5.0x10'1.0x10'5.0x10'l.HxlO2 • 92.4x10'2
1.2x10'
8.0x10'10
4.8x10'2.17.32.231.62x10'
1.6x10'
1.42xl0'9.27.81.67x10'1.13x10'6.0
Soil S4 (WIRE)Soil lib (Leanlngton)Soil IP (CR.NL)Soil 118 (North Bay)Soil »IO (VtJRE)Soil #11 (UffiE)Soil W3 (C.F.B. Borden)Soil »16 (Alberta)Sediment B (Solution 1)Cbnposlte soilRiver sand
ftaford subsoil
Hmford subsoUSldell sand
Burbank soilBurbank soUBurbank soilBurbank soilBurbsnk sand (average profile)
fyhrata sand (average profile)
Chalk River (CR) aquifer sandChalk River (RA) aquifer sandChalk River (Q) aquifer sandChalk River (SB) aquifer sandChalk River 00 aquifer sandChalk River (HA) araiifer sand
Gillhamet a l . , 1981aGillham et a l . , 1981aGillham et a l . , 1981aGlllhan et a l . , 1981aGlllhsm et a l . , 1981aGillham et a l . , 1981aGillham et a l . , 1981aGillham et a l . , 198LaSeme et a l . , 1978Sctaal*. 1972Hratra S Vertetk, 1977
Rhodes, 1957
Rx>des, 1957Juo b Barber, 1970
llajek S. ta, 1968fejek i J tes, 1968H3jek 4 tees, 1963Hajek I tes, 1968Houcson, 1973
Rojtson, 1973
Patterson & SpDel, 1981Patterson i Spoel, 1981Patterson & Spoel, 1981Patterson & Spoel. 1981Patterson & Spoel, 1981Patterson 5 Spoel, 1981
ro
I
TABLE 25 (Collided)
SoU 7. :
Type Sand Sil t
Silt 363534281234
45
35363541553444
7. 7.
Clay Organic
29
2131313332
11medlun lonn 31.6
medlun 1c
31381840
34457
183
696266455247927196
s U t
44Clay 31
heavy
heavy
heavy
5034lcs
0.430.410.401.270.350.850.142.94
(0.01 am)m 41.6
(0.01 mn]00
1615148
1111
29.1
635
c 53.41(0.01 am)
losm 46.67.(0.01 on)
loan 67 .Wrn m ™.\
clayey 60.7Z(0.01 am)
100Z (<0.02 nn)
Organic muck '
1.28
----
-----
7 .1
0.230.812.04
-
4.87
6.86
-
(9.8
7.
CaCO,
33.633.834.121.10
5.11.4-
-
----
-----
-
3.85.2-
-
-
_
-
Saturated Pasts (V)
8.1 (OC12)8.1 (CaCl2)8.1 (CaCl2)7.7 (CaCl2)6.7 (CaCl2)7.7 (CaCl2)8.83 (CaCl,)
6 .6
8.4
----
--
- ---
6
„
7.8 (CaCl-,)6.6
6.7
8 .0
6.8
-
7 . 0
CEC 7. Free(meq/100 g) Iron Oxide
8.48 .38.65.9
10.232.712.010.6
12.2
2.62.76.31.84 . 91.54 .2
3.55.2
39.4
11.0 1.2131.526.1
30.4
32.9
32.2
35
70.0
Competings Cation
see ref .see ref.see ref.see ref.see re f .Bee ref.see ref .
-
-
----
-----
3xlO"3 rol/L
StClo*0.2 rol/L Nadsee ref.
-
-
-
_
-
3x10-3 ml/ISrCl2
(°i./g)
2.0x10'2 .0x10 '2.0x10'1.0x10'l.OxlO2
8.01.12xlO2± 13.OxlO2 ±
1.7X102 ±
1.4x10'2.3x10'1.8x10'1.6x10'1.6x10'1.4x10'2.2x10'1.6x10'1.6x10'5.0x10'
2.47x10'85.7xlO2 +
l . tSx lO 3 :
A.3X102 ±
A.9X102 t
4 .7x10 '
l .SxlO 2
60
30
80
SoU Locationor Description
Soi l #1 (WRE)SoU #2 (WTO)SoU »3 (VKRE)SoU K (Leanlngton)SoU m (North Bay)SoU #14 (Albert*)Sediment A (Solution I)low ash podzollc
Serozafl
alluvial soil (Cadarache)alluvial soil (Cadarache)Vlndobonian sed. (Cadarache)Vlndobonlan sed. (Cadarache)Vlndobonian sed. (Cadarache)Vlidobonlan sed. (Cadarache)sandy-day Bed. (Durance R.)sandy-clay sed. (Durance R.)sandy-day sed. (Durance R.)Brookston s U t
RitzvUle sUt (avg. profile)Soil #15 (Alberta)Chestnut
t 140 Leached Chernozem
X
50
Southern Chernozem
Thick Chernozem
very fine suspaded oedinent(Durance River)Muck
Reference
Glllhai et a l . , 1981aGUlham et a l . , 1981aGOJhai et a l . , 1981aGlllham et a l . , 1981aGUlham e t a l . , 1981aGil lhao e t a l . , 1981aSeme e t a l . , 1978A l e k s a k h K 1965
Aleksakhin, 1965
Rancon, 1972Rsncon, 1972Rancon, 1972Rsncon, 1972fancon, 1972Rjncon, 1972Rancon, 1972Rancon, 1972Rancon, 1972Juo 5 Barber, 1970
Routson, 1973Gillham e t a l . , 1981oAleksakhin, 1965
Aleksakhlit, 1965
Aleksakhln, 1965
Aleksakhin, 1965
Rancon, 1972
J<x> 4 Barber, 1970
Data available for competing cations sodlun, potasslun, magneslun, calclun, barlun and hydrogen.
- 44 -
SoilType
Sand
Silt
Clay
(mL/g)
26.02
49.49
449.2
S.
30.
72.
415
D.
21
44
.7
TABLE 26
Kj FOR STRONTIUM
n
26
20
6
Kd Range(mL/g)-
2.0 to 114
8.0 to 300
8.0 to 1150
1
1
2
LognormalDistributionH 0
.162 0.4964
.436 0.4254
.286 0.8239
Baes and Sharp (1981) suggested a mean value of 1.4 for the
log1QK, for strontium, with a corresponding standard deviation of 0.9 (see
Table 1). K values for strontium determined for various pure clay minerals
ranged from 0.2 to 9.0 mL/g (Wahlberg et al., 1965). K , values determinedd
for various minerals (including clay minerals) ranged from 0 mL/g for quartz
to 2.1 x 103 mL/g for alumina (both at pH = 7.5) in a natural water solution
and from 1 mL/g for quartz to 1.44 x 103 mL/g for alumina (both at pH = 7.0)
in a 0.1 mol/L sodium nitrate solution (Tamura, 1972). Palmer et al. (1981)
also reported extensive results for strontium sorption on pure clay, clay/
silica and alumina/clay for various solution compositions and pH. Allard et
al.(1977) reported a K, range of 20 to 63 mL/g for clay/mud and a range of 3
to 16 mL/g for granite. Vandergraaf (1982) recommended a K range ford
strontium of 0.6 to 600 mL/g for granite.
Strontium ReferencesAllard, B., H. Kipatsi and J. Rydberg. 1977. Sorption of long-lived radio-nuclides in clay and rock. Part 1. Determination of DistributionCoefficients. KBS Technical Report 55.
Aleksakhln, R.M. 1965. Radioactive contamination of soils and plants.USAEC Report AEC-tr-6631.
Baes III, C.F. and R.D. Sharp. 1981. Predicting radionuclide leaching fromroot zone soil for assessment applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
- 45 -
Gillham, R.W., L.E. Lindsay, W.D. Reynolds, T.J. Kewen, J.A. Cherry and M.R.Reddy. 1981a. Studies of cesium and strontium migration in unconsoli-dated Canadian geological materials. Atomic Energy Control Board Re-port, INFO-0049.
Hajek, B.F. and L-L. Ames, Jr. 1968. Strontium and cesium equilibriumdistribution coefficients: Batch and column determinations. BattellePacific Northwest Laboratories Report, BNWL-481-3.
Hamstra, J. and B. Verkerk. 1977. Review of Netherlands program for geo-logic disposal of radioactive waste. In: Nuclear Power and its FuelCycle. International Atomic Energy Agency Report, IAEA-CN-36/289.
Juo, A.S.R. and S-A- Barber. 1970. The retention of strontium by soilsinfluenced by pH, organic matter and saturation cations. Soil Sci.109, 143-148.
Palmer, D.A., S.Y.Shiao and R.E. Meyer. 1981. Adsorption of nuclides onmixtures of minerals. J. Inorg. Nucl. Chem. 3_, 3317-3322.
Patterson, R.J. and T. Spoel. 1981. Laboratory measurements of the stron-tium distribution coefficient K,Sr for seaquifer. Water Resour. Res. j7_, 513-520.tiura distribution coefficient K,Sr for sediments from a shallow sand
Ranc.on, D. 1972. Practical utilization of the distribution coefficient forthe measurement of the radioactive contamination of minerals in rocks,soil and subterranean water. Cardarache Nuclear CEA Research Center,ANL-trans-931, Report-R-4274.
Rhodes, D.W. 1957. The effect of pH on the uptake of radioactive isotopesfrom solution by a soil. Soil Sc. Am. Proc. 1_, 389-392.
Routsons R.C. 1973. A review of studies on soil-waste relationships on theHanford Reservation from 1944 to 1967. Battelle Pacific NorthwestLaboratories Report, BNWL-1464, UC-70.
Schmalz, B.L. 1972. Radionuclide distribution in soil mantle of the litho-sphere as a consequence of waste disposal at the National Reactor Test-ing Station, USAEC Report, IDO-10049.
Serne, R.J., D. Rai and S.J. Phillips. 1978. Monitoring and physical char-acterization of unsaturated zone transport: Laboratory analysis. In:Nuclear Waste Management Quarterly Progress Report 1977 Oct.-Dec.Pacific Northwest Laboratory Report, PNL-2377-4, UC-70.
Tamura, T. 1972. Sorption phenomena significant in radioactive waste dis-posal. Jji: Underground Waste Management and Environtaental Implica-tions. Araer. Assoc. Pet. Geol. Mem. 18^, 318-330.
- 46 -
Vandergraaf, T.T. 1982. A compilation of sorptlon coefficients for radio-nuclldes on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Wahlberg, J.S., J.H. Baker, R.W. Vernon and R.S. Dewar. 1965. Exchangeadsorption of strontium on clay minerals. U.S. Geol. Surv. Bull.,1140-C, U.S. Government Printing Office, Washington.
4.12 TECHNETIUM
The environmental behaviour of technetium has recently been re-
viewed (Turcotte, 1982), as has the chemistry of technetium (Paquette et
al., 1980). Technetium migration is generally retarded under reducing con-
ditions (i.e., in geological formations), where it is less soluble. Techne-
tium, however, moves with the groundwater in aerated soils of low organic
carbon content. Johnston and Gillham (1980) indicated that
(1) because the pertechnetate ion, TcO^, is the most stable species
of technetiuni in aqueous solutions, TcO4" will not be subject to
ion exchange; hence, technetium will show little adsorption to
soil;
(2) in soils with appreciable organic matter, Tc "• may be reduced to
and adsorbed.
The recommended K value means, standard deviations, ranges and distribu-
tion parameters for technetium by aoil type, based on Table 27, are given in
Table 28.
TABLE 28
SoilType
Sand
Silt
Organic
(mLy
29.39
1.426
118.4
S.D.
100.1
3.869
192.0
FOR
n
15
8
3
TECHNETIUM
1
1
K d Range(mL/g)
.0x10-3 to
.0x10-3 to
0.24 to
388
11
340
LognorraalDistribution
\i a
-1
-1
1
.148 1.565
.332 1.290
.029 1.581
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
TABLE 27
S i l l %Type Snnrt
S.ini 6787
87
87
53954077
'.9
59
59
59
4587
I
Silt
9
9
9
9
353
38114
4
4
4
44
9
day
4
4
4
4
122
221237
37
37
37
114
coarse <wndSilt 45
16
399
3727
8
Organic
44
52806457334360
1132172734303032
charcoal
fen
zOrganic
0.100.10
0.10
1.10
3.01.22.81.8
-
-
-
0.140.10
-0.148.32.35.4
11.07.32.43.1-
3.0 23.3
3phagrui peat 92
•C-COj
0.070.07
0.07
0.07
----
<0.2
<0.2
<0.2
<0.2
_
-8.21.4--------
-
4.9
* * •
Sflt'irated Raste fV) (r
fl.238.2 ortdizeii
10.1 reduzed
10.1 reduced
5.45.76.08.15.1
5.1
5.1
5.1
8.88.2
8.4 (inter)
s.n7.65.57.77.77.85.96.6
6.3 - 6.6
4.5
3.8 < o t e r )
VALUES FOR THHNnTLM
CF.C
rqAOO
5.05.0
5.0
5.0
15.23.2
20.411.7
2.5
2.5
2.5
2.5
_
-1.2
12.027.011.316.936.443.519.326.8
-
46
64.7
I Freeg) Iron Orides
--
-
1.10.60.70.2-
-
-
-
_
-1382 (yg/g)
-0.41.40.10.50.30.91.2-
0.55
1050 (t^/g)
: LITERATURE SURVEY SU+Blft
CocpetlngCation
see ref.
Na3 CitrateCit/Tc tblarRatio - 0N*3 Citrate
Cit/Tc * l a r
Ritlo - 0Sa3 Citratea t / I t MjlarRatio- 1:1
----
0.0O2 iml/L
0.008 iml/t
0.020 IIDI/L
0.200 DDl/L
.JaHCOj
-
see ref .
see ref.-------
K>Cl brine
0.01 or 0.05m l A CaQjsee ref.
Kd(nt/g
0.07 i 0.320.32 (5xlCT9 mol/LTc)
52 (5x10-9 ml/L
Tc)
388 (5xlCT9 m>l/LTO
O.L550.0510.0780.00040.019 1 0.06
-O.052 i 0.01*
-0^)33 1 0.01«
4OJJ10 t 0M
0.040.030.O94-2.77 tO.23«0.0280.0680.1180.U80.0760.0110.000340
0.24
15.0
Soil Locationor Description
Sediment B (solution 1)Itenford soil
Hmford soil
Hanford soil
Aqulc Fragiochrept (AJ-AJ)Alf lc UdlpsaniHit (B)Aqutc * P : U ± J 1 1 (Ap)Aqulc Haploboroll (Ap)South Carolina subsoil
Scuth Carolina stfrcU
South Carolina sUnoll
Scuth Carolina sufceoU
ixlsaturated columuns?turated coLmnsandSediment A (solution 1)Cunulic HaplaqinllTyplc Eutroboralf (Aj)Aertc CaldaquoU (Aj)Omillc ifapLjqioll (Ap)Typlc ibplaquoU (Al)Aqulc Ibpluloll (Al)Udlc Ibplohoroll (Ap)activated "Mxhar"
fen soil, Enraen (Netherlands)
sphagnun peat
Reference
Seme et a l . , 1978Franz et a l . , 1982
Franz et a l . , 1982
Franz et a l . , 1982
Balogh i. Crigal, 1980Balogh S Grlgal, 1980Jfelogh S Origal, 1980Balogh I Crigal, 1980Rcutaon et s i . , 1977
ftxitson et a l . , 1977
Routson et a l . , 1977
Routson et al., 1977
Gee I Caopbell, 1980Gee S Campbell, 1980Sheppard et a l . , 1983Seme et a l . , 1978ialogh & Crtgal, 1980Balogh 4 Crigal, 1980Balogh 4 Crigal, 1980Balogh 4 Crtgal, 1980Balogh 4 Gr'gal, 1980Balogh 4 Grtgal, 1980Balogh 4 Crigal, I960Norak, 1981
rbusny 4 tyttenaere.1981Sheppard et a l . , 1983
.6-•vl
* ?iegatlvQ values will fae considered as a zero value.
- 48 -
Eaes and Sharp (1981) suggested a mean value of -1.5 for the
log10K for technetium, with a corresponding standard deviation of 0.5 (see
Table 1). Mousny and Myttenaere (1981) investigated the effect of tempera-
ture on the soil adsorption of technetium and reported that, for seven soils
investigated (including a podzol soil and a fen soil), K, ranged from 0.007
to 0.234 mL/g. Baes and Sharp (1981) suggested the K range is 0.003 to
0.28 mL/g (see Table 1). Wildung et al. (1974) selected 22 surface soils
with the following range of properties:
CEC(meq/100
5.5-90.0
g)
3
PH
.6-8.9
Carbonate
0-6.5
OrganicCarbon
0.23-28.8 14
Sand- %
.1-73.1 17
Silt
.6-58.0 3
Clay
.8-46.6
and suggested that the K, for technetium ranges from 0.007 to 2.8 mL/g.a
Thay also suggested a prediction equation of the form
Kd = 0.08 X3 - 0.09 X4 (7)
where X. is the organic carbon content,
X, is the pH.4
Vandergraaf (1982) recommended a K, range for technetium of 0 to 80 mL/g ford
granites.
Technetium References
Baes III, C.F. and R.D. Sharp, 1981. Predicting radionuclide leaching fromroot zone soil for asse. lent applications. Oak Ridge National Labora-tory Report, CONF-810606-44.
Balogh, J.C. and D.F. Grigal. 1980. Soil chromatographic movement of 93Tcthrough selected Minnesota soils. Soil Science 130, 278-282.
Franz, J.A., L.Y. Martin and D.J. Wiggins. 1982. Behavior of reduced 99Tcand y9Tc organic complexes on Hanford soil. Pacific Northwest Labora-tory Report, PNL-4178, UC-70.
- 49 -
Gee, G.W. and A.C. Campbell. 1980. Monitoring and physical characteriza-tion of unsaturated zone transport - Laboratory analysis. PacificNorthwest Laboratory Report, PNL-3304•
Johnston, H.M. and R.W. Gillham. 1980. A review of selected radionuclidedistribution coefficients of geologic materials. Atomic Energy ofCanada Limited Technical Record, TR-90*.
Mousny, J.M. and C. Myttenaere. 1981. Absorption of technetium by plantsin relation to soil type, contamination level and time. Plant and Soil6l_, 403-412.
Nowak, E.J- 1981. Composite backfill materials for radioactive waste iso-lation by deep burial in salt. Scientific Basis Nuclear Waste Manage-ment 3_, 545-552.
Paquette, J., J.A.K. Reid and E.L.J. Rosinger. 1980. Review of technetiumbehavior in relation to nuclear waste disposal. Atomic Energy ofCanada Limited Report, TR-25*.
Routson, R.C, G. Jansen and A.V. Robinson. 1977. 2l4lAm, 237Np, and 99Tcsorption on two United States subsoils from differing weathering inten-sity areas. Health Phys. 3_3_, 311-317.
Serne, R.J., D. Rai and S.J- Phillips. 1978. Monitoring and physical char-acterization of unsaturated zone transport: Laboratory analysis. In:Nuclear Waste Management Quarterly Progress Report 1977 Oct.-Dec,Pacific Northwest Laboratory Report, PNL-2377-4, UC-70.
Sheppard, M.I., T.T. Vandergraaf, D.H. Thibault and J.A.K. Reid. 1983.Technetium and uranium: Sorption by and plant uptake from peat andsand. Health Phys. 44_, 635-643.
Turcotte, M.S. 1982. Environmental behavior of technetium-99. E.I. duPont de Nemours & Co., Savannah River Plant and Laboratory Report,DP-1644, UC-11.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Wildung, R.E., R.C. Routson, R.J. Serne and T.R. Garland. 1974. Pertech-netate, iodide, and methyl iodide retention by surface soils. BattellePacific Northwest Laboratories Report, BNWL-SA-5195.
4.13 TIN
Gerritse et al. (1982) suggested that the K, value for tin ranges
from 1 x 102 to 1 x 106 mL/g. We recommend that the K. distribution infor-d
mation for lead be used for tin.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario KOJ 1J0.
- 50 -
Tin Reference
Gerritse, R.G., R. Vriesema, J.W. Dalenberg and H.P. De Roos. 1982. Effectof sewage sludge on trace element mobility in soils. J. Environ. Qual.11, 359-364.
4.14 ZIRCONIUM AND NIOBIUM
Rhodes (1957) reported K, values ranging from 90 mL/g (pH = 6.0)
to > 1980 mL/g (pH = 2.7, 3.5, 4.4, 8.4 and 9.3) for zirconium-niobium ad-
sorption on Hanford subsoil. From this information, in the pH range of most
interest for surface soil (pH = 5 to 8, a sandy soil), zirconium has an
average K of 164 mL/g. This appears to agree well with the K, for niobiuma d
of 210 tnL/g recommended for granite (Vandergraaf, 1982). Vandergraaf also
recommended a K range for zirconium of 1000 to 6000 mL/g for granite.
Allard et al. (1977) reported a K range for zirconium of 50 to 1000 mL/g
for clay/mud and 1250 to 6300 mL/g for granite.
Based on this information, the recommended mean of the lognormal
distribution for zirconium and niobium is 2.5 with a standard deviation of
1.0. Because information is insufficient to break it down by soil type, one
value is recommended for all soil types.
Zirconium and Niobium References
Allard, B., H. Kipatsi and J. Rydberg. 1977. Sorptlon of long-li ed radio-nuclides in clay and rock. Part 1. Determination of DistributionCoefficients. KBS Technical Report 55.
Rhodes, D.W. 1957. The effect of pH on the uptake of radioactive isotopesfrom solution by a soil. Soil Sc. Am. Proc. 1_, 389.
Vandergraaf, T.T. 1982. A compilation of sorption coefficients for radio-nuclides on granites and granitic rocks. Atomic Energy of Canada Lim-ited Technical Record, TR-120*.
Unrestricted, unpublished report, available from SDDO, Atomic Energy ofCanada Limited Research Company, Chalk River, Ontario K0J 1J0.
- 51 -
5. DISTRIBUTION COEFFICIENTS FOR OTHER NUCLIDES
5.1 ANTIMONY
No specific soil K, information was found for antimony. The K
values for lead are recommended for antimony, because of its proximity to
lead in the Periodic Table.
5.2 BORON
Little information was found on boron adsorption on soils; how-
ever, there is some indication that adsorption is influenced by soil texture
and the presence of soluble salts and exchangeable cations (Gupta, 1980).
Boron adsorption information reported by Keren and O'Connor (1982) for mont-
morillonite and illite indicated that the K, value for boron for these pure
clays covld be as high as 20 mL/g. That work suggested that the K value
for soils may be in the range 0 to 10 mL/g. We recommend a value of 1 mL/g
for assessment purposes; the lognormal distribution parameter values cannot
be given.
Boron References
Gupta, I.C. 1980. Equilibrium adsorption of boron as affected by texturetsalinity and alkalinity of soil. Ann. Arid Zone _L9_, 243-248.
Keren, R. and G.A. O'Connor. 1982. Effect of exchangeable ions and ionicstrength on boron adsorption by aiontmorillonite and illite. Clays ClayMiner. 30, 341-346.
5.3 CADMIUM
Most of the work carried out with cadmium has been in response to
environmental concerns about the application of sewage sludge to agricultur-
al land. The sorption of cadmium on soils and sediments has been studied by
Poelstra et al. (1979), Rendell et al. (1980), Hendrickson and Corey (1981),
and Gerritse et al. (1982). The recommended K, value means, standard devia-
tions, ranges and distribution parameters for cadmium, based on Table 29,
are given In Table 30.
SoilType
Sand
SUt
ClayOrganic
I X XSand Silt day
sandy soil
sandy soil
sandy soil 0
sandy Mil 20
fine sand<74 m<74 m<74 yu
day soil 23organicpeat soU
sphagmiD peatsphagrun peat
plantation mjck
ZOrganic
-
-
3.5
2.5
1.40.721.81.56
16.39590
>90
>90
--
47
Z PH*CaX3 Saturated Paste
6.5
6.5
4.5 - 5.0
7.5 - 8.0
8.28.46.05.8
trace 7.45.2
5.1 (1U))4 . 5 ^
4 to5
6.2
4 to 54 to 5
7.2
K. VALUES FOR CADMIUM : LHHiAIURE SURVEY SUHARY .
Ev CEC I Free(V) (neq/100 g) Iron CWdea
31.6
31.6
- 22
- 16
- 1160 1.0725 1.0724 8.29
_33.8
_ -
- 34
CoipetlngCation
-
-
Ica«T0-0.015 train.
0-0.015 vein.-------
(a»i-0-0.015 mol/L[ C a » l -0-0.015 oo lA[ C a » l -0-0.015 nol/L
-0.025 HECaw/aL sol.
(nL7g)
66.7*
47.6*
2.62xlO2
5-OxlO2
72769.816625*23370*1.44xlO3
9.OilO3
5.7fctlO3
1.7riO>3x10'
341
SoU Locationor Description
Sandy soil (Braunschselg)0-20 cmSandy 8011 (Braunschuelg)30-40 cmSoU C
SoU D
n.11^4.1. f (jy. sandInpertal (California)Ollvcnhain (California)Bocoer (California)(Valburg) 0 - » csorganic(Schxnebeek)SoU A
Peat A
SoU B
PeatPeat
average of 3 layers
Reference
Poelstraet a l . , 1979
Poelstraet a l . , 1979
Gerrltse et a l . , 1982
Gerrltaeet a l . , 1982
Vbnget a l . , 1983Carcla-Wragaya, 1980Garcla-Wragaya, 1960Gareia-ttlragaya, 19B0PDelstra et a l . , 1979Gsrda-MlragaTB, 1980Poelstraet a l . , 1979Gerritse et a l . , 1982
Gerrlue et a l . , 1982
Gerritse et a l . , 1982
tblf et a l . , 1977Ifclf et a l . , 1977
Ubnget a l . , 1983
rO
I
1 ueck equilibration
- 53 -
TABLE 30
K3 FOR CADMIUM—d -
Soil KJ S.D. n KJ Range LognormalType (mL/g) (mL/g) Distribution
\i a
SandSiltOrganic
189.733.934246
194.136.566110
538
47.69.8
23
tototo
50076
1.7x10 *•
21
2
.095
.359
.880
001
.4397
.4645
.090
Hendrickson and Corey (1981) reported K data from several
authors, and their plot indicated that the K, range is 0 to 6 mL/g and isd
significantly dependent on both the cadmium and calcium contents of thesoil. Navrot et al. (1978) reported K, values for cadmium for five Israeli
d
soils ranging from 1 x 103 to 1 x 10 ** mL/g, and the K value was correlated
to specific soil surface area.
Cadmium References
Garcia-Miragaya, J. 1980. Specific sorption of trace amounts of cadmium bysoils. Commun. Soil Sci. Plant Anal. _11 , 1157-1166.
Gerritse, R.G., R. Vrlesema, J.W. Dalenberg and H.P. De Roos. 1982. Effectof sewage sludge on trace element mobility in soils. J. Environ. Qual.11 , 359-364.
Hendrickson, L.L. and R.B. Corey. 1981. Effect of equilibrium metal con-centrations on apparent selectivity coefficients of soil complexes.Soil Science 1_31_, 163-171.
Navrot, J., A. Singer and A. Banin. 1978. Adsorption of cadmium and itsexchange characteristics in some Israeli soils. J. Soil Sci. 29,505-511.
Poelstra, P., M.J. Frissel and N. El-Bassam. 1979. Transport and accumula-tion of Cd ions In soils and plants. Z. Pflanzenernaehr. Bodenkd.142, 848-864.
Rendell, D.S., G.E. Batley and A.J. Cameron. 1980. Adsorption as a controlof metal concentrations in sediment extracts. Environ. Sci. Technol.14, 314-318.
- 54 -
Wolf, A., K. Bunzl, F. Dietl and W.F. Schmidt. 1977. Effect of calciumions on the absorption of lead (2+), copper (2+), cadmium (2+) and zinc(2+) by humic substances. Chemosphere 6_, 207-213.
Wong, K.V., S. Sengupta, D. Dasgupta, E.L. Daly, Jr., N. Nemerow and H.P.Gerrish. 1983. Heavy metal migration in soil-leachate systems. Bio-cycle 24, 30-33.
5.4 TELLURIUM
Allard et al. (1977) suggested that the K value for tellurium for
clay/mud and granite is 1 mL/g. This work suggests that the K range may be
0 to 1 mL/g. We recommend a K, value of 0 mL/g for assessment purposes; no
distribution parameter values can be given.
Tellurium Reference
Allard, B., H. Kipatsi and J. Rydberg. 1977. Adsorption of long-livedradionuclides in clay and bedrock. Part 1. Determination of distribu-tion coefficients. KBS Technical Report 55.
5.5 ZINC
Gerritse et al. (1982) suggested that the K, values for both zinca
and cadmium range from 1 x 103 to 1 x 10 "* mL/g, and their data for sandy and
organic soils show that the two elements exhibit very similar sorption be-
haviour. The recommended K, value means, standard deviations, ranges and
distribution parameters for zinc, based on Table 31, are given in Table 32.
SoilType
Sand
Silt
Organic
(mL/g)
622.0
51.8
4092
S.D.
911.6
68.17
4909
TABLE
K FOR
n
5
2
6
32ZINC
K^ Range(mL/g)
0.1 to 2120
3.6 to 100
70 to 1.3x104
1
1
3
LognormalDistribution\i a
.762 1.694
.278 1.021
.185 0.83
IABLE31
K. VALUES P3i ZDC ; UTEBAUJKE SURVEY SUMUg
Soi l % X S 7. Z pH* & (EC Z Free CountingType Sard Silt Clay Organic CaCD3 Saturated Paste (V) (raeq/100 g) Iron Oxides Cation (ni.7g)
Soil Uicatlonor Description
Sard
Silt
Organic
sandy soli
sandy soil
flrv sandsi l t lofnsi l t loanorganic
organic
orgpnlc
sphagrvQ peatsphagrun peat
3.5
2.5
1.4
90
m
>9O
:
4.5 - 5.0
7.5 - 8.0
4.86.28.25.07.44.5
4 - 5
6.2
4 - 54 - 5
22
16
11
7.2
7.0xl0l Soil C Gerrltse et a l . , 19820-0.015 ml/I .
[G>2+1-0-0.015 rol/L
0.1 nnlfl. CaClj0.1 rol/L CaCl2
-0.1 rol/L CaCl20.1 rol/L CaCLj(Ca2*] •0-0.015 aol/L
[Ca2*] -0-0.015 irol/L
fCa2*] •0-0.015 ml/L
-0.025 neqCa2+/nL sol.
2.12X1O3
0.1508703.61001.89idO3
6.3T1O3
2^8xl03
UulO"7.CW01
Soli D
Horlda 1Florida 2Kallandale fine sandMissouri 23Missouri 24Soil A
Peat A
SoU B
PeatPeat
Gerrltse et a l . , 1982
Graham, 1973Graham, 1973Ubnget a l . , 1973GrahD, 1973Graham, 1973Cerrltae ec a l . , 1982
Gerrltse et a l . , 1982
Gerrltse ec a l . , 1982
Hjlf et a l . , 1977Vblf et a l . , 1977
Plantation suck (averageof 3 layers)
Vot% et a l . , 1983
I
- 56 -
Zinc References
Gerritse, R.G., R. Vriesema, J.W. Dalenberg and H.P. De Roos. 1982. Effectof sewage sludge on trace element mobility in soils. J. Environ. Qual.U^, 359-364.
Graham, E.R. 1973. Selective distribution and labile pools of micronutri-ent elements as factors affecting plant uptake. Soil Sci. Soc. Amer.Proc. 21, 70-74.
Wolf, A., K. Bunzl, F. Dietl and W.F. Schmidt. 1977. Effect of calciumions on the absorption of lead (2+), copper (2+), cadmium (2+) and zinc(2+) by humic substances. Chemosphere 6_, 207-213.
Wong, K.V., S. Sengupta, D. Dasgupta, E.L. Daly, Jr., N. Nemerow and H.P.Gerrish. 1983. Heavy metal migration in soil-leachate systems. Bio-cycle 24_, 30-33.
5. CONCLUSIONS
The paucity of K, values for organic soil is the most striking
observation from our review of the literature. Plutonium, lead, technetium,
cadmium and zinc were the only nuclides for which more than two K, valuesd
have been determined for an organic soil (see Table 33). The next most
important observation is that very little work has been done with mineral
soils for some of the more mobile nuclides with K, values up to 100 mL/g,
such as uranium, technetium, molybdenum, iodine, selenium, carbon, boron,
and tellurium. There may be good reasons why more K, work is not warranted
for these nuclides in the Canadian waste management program, such as the
formation of precipitates or reduction to an immobile species in the vault
or geosphere. Our major recommendation is that effort be directed towards
the chemistry (including parameter determination, i.e., K, determinations)
of organic soils, and in particular the reactions of uranium, technetium,
iodine, selenium and carbon with organic soils. In spite of the limited
data base, it is possible to select reasonable K distribution parameter
values for most nuclides for long-term waste management assessment
purposes.
- 57 -
AVAILABILITY
Nuclide
ActiniumAmericiumAntimonyBismuthBoronCadmiumCalciumCarbonCesiumIodineLeadMolybdenumNeptuniumNickelPalladiumPlutoniumPoloniumProtactiniumRadiumRare EarthsSeleniumSilverStrontiumTechnetiumTelluriumThoriumTinUraniumZincZirconium & Niobium
X denotes 2 or fewer KJ
TABLE
OF Kd DATA FOR
Sand
X
X
X
XX
X
XX
X
XXX
XXXX
X
, values.
33
EACH NUCLIDE
Soil
Silt
X
X
X
XX
XX
XX
X
XXX
XXXXXX
BY SOIL TYPE
Type
Clay
X
XXXXXX
XX
XX
XX
XXX
XXXX
XX
Organic
XXXXX
XXXX
XXXX
XXXXXXX
XXXX
X
- 58 -
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