United States
                   Environmental Protection
                   Agency
Water Engineering
Research Laboratory
Cincinnati OH 45268
                   Research and Development
EPA/600/S2-85/053 Sept. 1985
&ERA         Project  Summary
                   Determination  and  Prediction  of
                   Chemical  Forms of  Trace
                   Metals  in  Sewage Sludge  and
                   Sludge-Amended Soils
                   L. J. Lund, G. Sposito, and A. L. Page
                     A computer program. GEOCHEM,
                   was developed to calculate trace metal
                   equilibria in soil solutions affected by
                   the application of sewage sludges. The
                   structure of the program, data required.
                   and typical applications of metal speci-
                   ation in aqueous extracts from munici-
                   pal sewage  sludges  and sludge-
                   amended  soils are described  and
                   discussed.
                     Fulvic acids extracted from sewage
                   sludge were found to contain 20 to 40
                   times  more  sulfur than fulvic acids
                   extracted from soil organic matter. Sul-
                   fonyls and surfhydryls therefore play a
                   significant role in the complexation of
                   metals in sludges and probably also in
                   sludge-amended soils. The partitioning
                   of metals in the organic and inorganic
                   aqueous  phases from  sludge and
                   sludge-amended soils  differs among
                   sludges. In general, Cu(ll) and Fe(lll)
                   show high preference for organic com-
                   plexation, and Cd, Ni, and Zn tend to
                   form  inorganic  complexes  preferen-
                   tially. Following equilibrium of sludges
                   from seven treatment plants with three
                   soils for a period of 50 weeks at 1 /3 bar
                   saturation, essentially all of the soluble
                   Cu was  organically complexed, and
                   most of the soluble Cd, Ni, and Zn were
                   present in solution as the free divalent
                   ion.
                     A procedure to fractionate sludges
                   into various chemical forms was devel-
                   oped.  The procedure  consisted of
                   extraction with KNO3 (exchangeable),
                   followed by distilled, deionized water
                   (adsorbed). 0.5 M NaOH (organically
                   bound), Na2 EDTA (carbonate), and
HNO3 (sulfide-residual). The  distri-
bution of metals in various forms fol-
lowing equilibration  of  soils  with
sludges is presented and discussed. In
general, only very small percentages of
the total quantity of metals in sludge-
amended soils occur in soluble, exchan-
geable, or adsorbed forms.

  This Project Summary was developed
by EPA's Water Engineering Research
Laboratory, Cincinnati. OH. to announce
key findings of the research project that
is fully documented in a separate report
of the same title (see  Project Report
ordering information at back).

Introduction
The use of land for the disposal or recy-
cling  of municipal sewage sludges has
increased during the past decade and is
continuing to grow. Sewage wastes are
receiving increased attention for use as
phosphorus fertilizers, supplemental nit-
rogen fertilizers, and soil conditioners.
Evidence exists that trace metals in
sludge-amended  soils  are toxic  to a
number of plant species, are  accumu-
lated  by many types of vegetation, and
may be a source of surface water and
groundwater  contamination. The  basic
chemistry of trace  metals in sewage
sludges and sludge-amended soils thus
needs to be fully understood. The reac-
tion rates, mechanisms, and products of
trace metals following their application to
soils in the form of sewage sludge are not
well known. The soluble and insoluble
forms in  sludge-amended soils will be
important in determining plant availabil-

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ity, toxicity, and mobility of trace metals.
This project investigated the chemical
forms of five trace metals (Cd, Zn, Ni, Cu,
and Pb) in municipal sewage sludges and
the changes that occur in them following
sludge application to soil as influenced by
time, sludge source, soil characteristics,
and solution composition. This informa-
tion will help determine conditions under
which  sludges can be safely recycled on
agricultural land,  and it will aid in the
selection of the most desirable soils for
disposal of sludges.  The  data  will also
serve as a basis for determining potential
degradation of soils and waters by sludge
application to land.
  Sewage wastes vary greatly with the
treatment plant, the time spent at any
one treatment plant, and the treatment
process. Because anaerobically digested
sludges represent  the  highest  percen-
tage of those  generated  in the United
States, this project emphasizes anaerobi-
cally digested sludge. Because of varia-
tions  in the trace  metal contents of
sludge from different treatment facilities,
sludges from a number of wastewater
treatment plants were investigated.
Description of GEOCHEM
  GEOCHEM is a computer program that
enables the calculation of trace metal
equilibria in soil solutions of widely vary-
ing compositions.  The program  was
developed and tested for use with sludge-
amended soils. The method of calculation
is based on chemical thermodynamics. A
mole balance equation is set up for each
component of a soil solution and thermo-
dynamic equilibrium constants corrected
for ionic strength  are incorporated into
the various terms of this equation accord-
ing to the law of mass action. The solu-
tion of the  set of  nonlinear algebraic
equations that results  from  simultane-
ously  applying mole balance to all the
components ultimately provides the con-
centration of each  dissolved,  solid, or
adsorbed species i n the soiI system under
consideration.

Applications of GEOCHEM
   Some typical applications  of  GEO-
CHEM would include: (1) predicting the
concentrations of inorganic and organic
complexes of a metal cation in a soil solu-
tion, (2) calculating the concentration of
a particular chemical form of a nutrient
element in a solution bathing plant roots
so as to correlate that form with nutrient
uptake, (3) predicting the fate of a pollu-
tant metal added  to a soil  solution of
known characteristics, and (4) estimat-
ing the effect of  changing pH,  ionic
strength, redox potential, water content.
or concentration of some element on the
solubility of a chosen chemical element
in a soil solution.
  To illustrate the application of GEO-
CHEM, Table 1 lists the analytical data for
a saturation extract of an Altamont soil
amended  with  sewage  sludge  and
CdS04  . In this example, there were 9
metals (including  H+ and  15  ligands
(including OH") that could form 261 dif-
ferent complexes according to the ther-
modynamic data  in the program.  The
output from a GEOCHEM subroutine for
the data in Table 1 appears in Table 2. The
percentage distribution figures for the
metals and ligands constitute considera-
ble worthwhile information,  but what
stands out is the strong complexation of
Cu(ll) and Fe(lll) by the organic ligands
and the relative lack of complexation of
Cd, Mn(ll), and Zn. The major cations, Ca,
Na, and K, are involved principally with
the inorganic part of the system, whereas
Cu(ll) and Fe(lll) are involved principally
with the  organic  part. The remaining
minor  cations Cd, Mn(ll),  and Zn, fall
somewhere in between.

Results
Analytical Properties of the
Fulvic Acid Fractions of
Three Sludges

An understanding of the mechanisms
through which sewage sludges incorpo-
rated in soil form water-soluble com-
plexes with trace metals should provide a
basis for predicting and controlling levels
of these metals in the soil solution. In
view of the existing literature on metal
complexation by components of natural
soil organic matter, it is reasonable to
suggest that  the fulvic acid fraction of
sludge and of sludge-amended soil would
be a major ligand for the complexation of
trace metals. The fulvic acid fractions of
three sludges were, therefore, extracted,
purified, and then studied for their ana-
lytical properties. The main  difference
between the fulvic acids  extracted from
sewage sludge (SS fulvic acids) and the
fulvic acids  extracted from  soil, organic
matter  (SOM  fulvic acids) is that  the
former  contain 20 to 40 times more S
than a typical  fulvic acid  extracted from
natural soil organic matter (Table 3). Two
of the SS fulvic acids also had somewhat
less oxygen than a typical SOM fulvic
acid.  The principal conclusions  to be
drawn from  these data are that SS fulvic
acids can  show significant  variability in
their chemical compositions, but that S-
containing components should exert an
important  influence on their chemistry in
any case.
  Ultraviolet and visible spectra of the SS
fulvic acids suggested thatthey consist of
highly aromatic and  condensed struc-
tures, somewhat comparable with those
in SOM humic acids. The aromatic nature
of the SS fulvic acids could be inferred
indirectly  from  their X-ray  diffraction
patterns, which yielded a y -band cen-
tered more  nearly at 4  than 5A, thus
implying a relatively small content of ali-
phatic components.


Partitioning   of  Metals  after
Sludge Incorporation into Soil
  At present, the chemical mechanisms
by which potentially harmful trace metals
in sewage sludges become  soluble spe-
cies after the incorporation of sludge into
soil are not well defined.  However, data
obtained in  this  study show that  the
  Table 1.    Analytical Data for a Saturation Extract of an Altamont Soil Amended with Sewage
            Sludge and CdSOS


 Component     pCf        Component
Ca
K
Na
Fe(lll)
Mn(ll)
Cu(ll)
Cd
Zn
CO
so.
Cl
2.07
3.70
3.00
4.75
4.70
5.72
5.85
5.13
2.70
2.70
2.28
P04
N03
Citrate^
Salicylate J
Phthalate J
Arginine $
Ornthine t
Lysine \
Valine J
Maleate J
Benzylsulfonate |
4.00
2.77
4./4
4.27
3.97
4.49
4.36
4.36
4.36
3.97
4.27
»  pH=6.30.
f  pC = - log [ ], where [ ] refers to a molar concentration.
t  Collectively considered organics in Table 2.

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Table 2.    Output from GEOCHEM Giving Primary Distribution of Metals and Ligands for Sludge-Amended Altamont Soil
                Free
Metal or
Ligand
Ca
K
Na
Fe(lll)
Mn
Cuflll
Cd
Zn
C°3
so3.
Cl
P04
NO3
Organics
Metal or
Ligand
88.6
99.0
98.8
—
77.8
0.3
62.2
69.9
—
69.8
98.4
—
93.2
17.9
Bound With
H
—
—
—
—
—
—
—
—
96.6
—
—
77.2
—
58.2
Ca
—
—
—
—
—
—
—
—
2.6
29.6
1.6
22.3
0.8
21.3
Na
—
—
—
—
—
—
—
—
—
0.5
—
0.1
—
2.2
Fe(lll)
—
—
—
—
—
—
—
—
0.5
—
—
—
—
0.02
Mn Cu(ll) Zn
— — —
— — —
— — —
_ _ _
— — —
_ _ _
— — —
— — —
0.1 — —
— — _
— — —
0.3 - -
_ _ _
0.3 0.01 —
C03
0.6
—
0.1
20.6
11.9
0.1
1.7
18.5
—
—
—
—
—
—
so.
6.9
0.6
0.9
—
6.1
—
4.9
6.9
—
—
—
—
—
—
Cl
1.0
—
—
—
0.2
—
17.2
0.1
—
—
—
—
—
—
P04
0.3
—
—
—
1.4
—
0.5
0.7
—
—
—
—
—
—
N03
0.6
0.3
0.1
—
1.4
—
1.1
—
—
—
—
—
—
—
Organics
0.19
—
—
79.3
2.2
99.2
12.4
3.7
—
—
—
—
—
—
Table 3.    Ultimate Analyses* of SS Fulvic Acids and SOM Fulvic Acids
Fulvic
Acid
Component
C
H
N
ot
S

Sludge A
30.3 ± f.7f
5.20 ±0.76
1.77 ±0.18
51.1
11. 56 ±0.95
SS Fulvic Acid
Sludge B1
45.2 ± 3.0
7.31 ± 0.28
3.06 ± 0.06
40.0
4.46 ± 0.65

Sludge C
46.95 ± 0.84
7.21 ± 0.05
3.67 ± 0.14
35.7
8.44 ± 0.42
SOM
Fulvic Acids
40-55
1.5 - 7.0
0.7 - 3.5
39-50
0.1 -3.6
  * Percentage, water- and ash-free basis.
  f Mean deviation computed on data for three different samples of fulvic acid.
  t Calculated by difference: %O-100-% CC+W+/V+S/
organic constituents of sludges play a
significant role  in  the  speciation of
metals such as Cd, Cu, Ni, Pb, and Zn. The
degree  to which  soluble  complexes
between  these   metals and  sludge-
derived organic compounds actually form
in a soil solution depends on the func-
tional group character and the water sol-
ubility of the organics, as well as on the
number and  stability of other possible
trace metal  compounds  and  surface
phases.
  The association  of five trace metals
with the organic  and inorganic fractions
was studied by eluting sludge-FA from
Sephadex G-10 columns.
  An elution diagram for a metal-SS ful-
vic acid solution  is shown in Figure 1 as
an example of these studies. The relative
concentrations of fulvic acid, Ni, and Cl
vary with elution volume, and relation-
ships between these concentrations can
be used to infer  something  about metal
complexes present. Results showed that
the partition  of  metals among  organic
and  inorganic  forms  differs  among
sludges. In general, Cu and Fe(lll) show
high preference  for  organic complexa-
tion, while Cd, Ni,  and Zn tend  to form
inorganic  complexes  preferentially.
These kinds of differences reflect clearly
the fact  that the complicated,  hetero-
geneous  nature of sludge-derived fulvic
acid makes for a detailed scheme of metal
binding that  will  depend on  the exact
molecular composition of a given sludge.

Incubation Studies to Evaluate
Changes  in Soils after Sludge
Amendment
  A number of factors such as aeration
and soil characteristics are  known to
affect  the  decomposition  of  organic
materials and the fate of the constituents
of the organic materials. For a fuller eva-
luation of the changes that take  place
when sewage sludge is added to soils, a
series  of incubation  experiments  was
carried out. In the first study, three soils
were amended with Ontario sludge.  Re-
covery of added trace metals by HNO ,
DTPA (diethylenetriaminepentaacetate),
and HOAc (acetic acid) was significantly
affected by water content, sample prepa-
ration, and soil. Application rate was gen-
erally not a significant factor.
  This work demonstrated  that for  soil
amended with Ontario sludge, metal
extractability varied  with  time, water
content,  sample preparation, soil, and
extractant. However, these results were
only for  one sludge. To determine the
effects of these treatments  more fully,
additional studies were conducted using
seven sludges representing  a range  of
characteristics.
  The factors and  levels  used in this
study were sludges (7), incubation water
contents (1/3 bar and saturated), soils
(Baywood,  Delhi,  and  Calhi),  sample
preparation (wet and air-dried), times (7),
and extractants (HNO3), DTPA, and sat-
uration extracts). A constant rate of 100
T/ha was used, because in the previous
study, rate did not affect the recovery of
metals by HN03 or DTPA. The mean re-
covery of the trace metals (Cd, Cu, Ni, and
Zn) added to soils in sludges by extraction
with 4/V HNO, was essentially complete
(>90%). On the average, metal recovery
by DTPA was 38%—less than half that of
HNO3. The recovery of metals by DTPA
varied from 34% for Pb to 43% for Zn.
Incubation time (1  to 52 weeks) had
essentially no effect on the amounts  of
metals  extracted   from the sludge-
amended soils by DTPA. Metal extracta-
bility was significantly less for samples
incubated at saturation than for samples
incubated at 1/3 bar water content.
  Saturation extracts of sludge-amended
soils incubated for 50 weeks were ana-
lyzed for cationic and anionic composi-
tion. These  data were analyzed using
GEOCHEM to predict the forms of the
trace metals in the soil solutions. Data for
Cd  are  used  to illustrate  the results
(Table 4).
  Cadmium was found to be present  in
the extracts  principally as  free  ionic
forms, with smaller percentages present
as organically complexed. For samples
incubated at 1 /3 bar, the only real excep-
tion to this result was for the LA liquid
sludge, in which inorganically complexed

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        120
                   150
      200

Elution Volume, ml
                                                      250
                                                                        300
Figure 1.    Elution diagrams for Ni in metal-fulvic acid solutions
Cd accounted for the greatest proportion
of Cd in the extracts. Incubation at satu-
ration resulted in a shift in form from free
ionic  to organically  complexed.  This
result occurred in every case where Cd
was detectable in the saturation extracts
of the samples incubated at saturation.

Fractionation Procedure
  A fractionation procedure was devel-
oped and used on sludge-amended soils
          to  estimate the  proportion of selected
          trace metals in various forms. The proce-
          dure consisted of extraction with KN03
          (exchangeable) followed  by  distilled-
          deionized water (adsorbed), 0.5 M NaOH
          (organically bound), Na,  EDTA (carbon-
          ates),  and HNO3 (sulfide residual). The
          use of distilled water to remove adsorbed
          metals was evaluated with freshly pre-
          pared Fe and Al hydrous oxide gels (Table
          5). Close to 100% recoveries of sorbed
metals were obtained for metals (Cd, Ni,
and Zn) having  the least affinity  for
adsorption  by the hydrous oxides. The
lowest  recoveries (approximately  80%)
were observed for Cu, which  had the
greatest affinity for both Fe and Al gels.
Recovery of Pb from the Fe gel was also
low. Recovery for each metal was virtu-
ally independent  of  the amount  of
adsorbed metal present at the  onset of
the extraction. These data suggested that
the  use of  three  sequential deionized
water washings forms a reliable basisfor
the extraction of adsorbed metals from
sludges and sludge-amended soils.
  The standard procedure for removal of
fulvic and humic acid fractions of organic
matter is by extraction with NaOH. This
extractant was therefore used to evalu-
ate  the proportion of  organic-bound
metals.  Data for the extraction of metals
from pure carbonates and sulfides indi-
cated that 0.5 M NaOH should be reason-
ably  specific  to  the  extraction  of
organic-bound  metals  (Table 6).  Only
with Pb and Zn were significant quanti-
ties of each metal carbonate brought into
solution by 0.5 M NaOH. The use of a
single 0.05  M NaEDTA extraction was
generally  specific to carbonate-bound
metals.  Only  small  proportions of the
metals  were extracted  from  the metal
sulfides using  this reagent. Essentially
complete recovery of metals from the cor-
responding metal sulfides was achieved
only after extraction with 4/V  HNO at
80°C (Table 6).
Table 4.    Speciation of Cd in Saturation Extracts of Sludge-Amended Soils After 50 Weeks of Incubation (percent of total)
Incubation
Water
Content Soil Species
1/3 Bar Bay wood F*
1
O
Delhi F
1
0
Calhi F
1
0
Saturation Baywood F
1
0
Delhi F
1
O
Calhi F
1
O

Rialto
58.6
22.0
19.1
75.2
20.6
4.2
75.7
19.9
4.1
-t
33.3
34.9
31.7
39.1
17.0
40.9

LA Compost
68.1
29.8
2.0
72.0
26.0
1.7
71.4
25.9
2.6
41.8
14.8
43.2
—
—

Colton
52.0
23.5
24.3
74.0
19.7
6.2
70.2
18.9
10.7
—
33.4
40.5
25.6
—
Sludge
Ontario
70.9
26.0
3.1
71.0
22.2
6.6
68.4
21.0
10.3
24.8
6.2
69.0
30.3
30.3
39.2
—

Escondido
54.4
36.5
9.0
67.8
29.5
3.0
64.2
31.7
3.9
41.7
23.4
34.8
42.4
26.4
31.1
—

LA Liquid
37.6
58.0
4.3
42.9
54.9
2.0
41.2
52.5
5.3
24.8
60.0
14.9
31.9
43.1
25.0
26.3
58.0
15.6

Kokomo
73.3
23.1
3.5
79.7
15.9
4.2
72.2
23.4
4.4
61.1
29.3
9.6
—
52.7
31.8
15.4
 * F = free ionic; I = inorganically complexed; O = organically complexed.
 f Indicates metal concentration below detection limit.

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Table S.    Water Extraction (3X) of Metals Absorbed by Fe and Al Hydrous Oxide Gels
  Metal
                      FeGel
                                            AIGel
 Sorbed    Extracted
 Percent
Recovery
Sorbed   Extracted
 Percent
Recovery
             (tig/0.05 g gel)
                                  (ug/0.05 g gel)
Cd
Cu
Ni
Pb
Zn
21.2
40.0
50.0
99. 4
25.2
37.6
50.0
100.0
38.0
64.6
21.8
41.2
41.0
93.5
26.2
38.0
41.4
80.6
36.4
63.1
102
103
82
94
104
101
83
81
96
98
6.2
16.0
48.8
97.6
14.6
28.0
44.0
89.6
38.6
73.0
6.5
16.6
36.1
81.0
14.3
24.4
45.5
91.6
38.8
69.8
105
104
74
83
98
87
103
102
101
96
 Table 6.
Extractant
Percent Recovery of Metals During NaOH. EDTA. and HNOa Extraction of 0.03 g of
Pure Metal Carbonates and Sulfides
                   	Metal Extracted
        Cd
                               Cu
            Ni
          Pb
  Zn
0.5 M NaOH
0.05 M EDTA
0.5 MNaOH
0.05 M EDTA
2 N HN03
4NHN03.80°C
0
99
0
4.3
16.3
98.7
1.1
100
1.3
3.3
0
47.5
Carbonate
0
1OO
Sulfide
0
15
46.2
100
38.5
85.1
8.8
20
44.9
100
33.2
100
0
0
94.0
1OO
amounts of sulfide-bound Cd relative to
the amount of Cd in this form after incu-
bation at saturation. Furthermore, for the
Calhi and  Delhi  soils, the amounts of
sulfide-bound Cd after 1/3-bar incuba-
tion were  usually  lower than  those
observed for the whole sludges.
  In the case of the Kokomo sludge,
which had a very high (81 %) proportion of
Cd  in the carbonate fraction, there was
tendency for Cd to be redistributed  into
the organic-bound and adsorbed frac-
tions during incubation. In fact, adsorbed
Cd at detectable levels was observed only
in the case of incubation with Kokomo
sludge.
  No  detectable,  exchangeable Cd was
observed after incubation of any of the
sludge-amended  soils,   reflecting  the
absence of  this  form   in  the  whole
sludges. Where applied sludges resulted
in Cd contents above 2  (ig/g of soil, a
of soil, a significant proportion (0.1% to
2.2%) of the total Cd appeared in solution
after incubation at 1/3 bar.
  The full report was submitted in fulfill-
ment of Grant No. R-804516 by the Uni-
versity  of   California  under  the
sponsorship of the U.S.  Environmental
Protection Agency.
  Again, the data for Cd are used as an
example of the results of applying this
fractionation  procedure  to  sludge-
amended soils (Table 7). When the study
used  sludges  with a  low Cd  content
(Rialto,  LA-composted,  and Cotton),
which resulted in Cd contents of less
2 /ug/g for the sludge-amended soils, Cd
appeared  almost  exclusively  in  the
organic and carbonate forms for each soil
amended with these sludges. The ten-
dency  was for the  distribution to  be
weighted in favor of the carbonate form
(14 out of 18 cases) despite the greater
proportion  of Cd in the organic form in
two out of three sludges.
  Though a small proportion of the total
Cd (7.3% to 17.1%) was present in the
Rialto,  LA-composted,  and   Colton
sludges  in the sulfide form, only in one
instance was  Cd observed in this form
after incubation  of the sludges with the
soils. In  contrast, the absence  of Cd in
exchangeable and adsorbed fractions in
the whole  sludges was maintained after
incubation. Only in one  instance (after
the incubation of Rialto sludge with the
                               Baywood soil at 1/3 bar) was any sub-
                               stantial quantity of Cd measured in the
                               soil  solution.  Only  minor  variations
                               occurred in the distribution of Cd for
                               these sludges as a result of the different
                               incubation  conditions employed.
                                All but one of the remaining sludges
                               with higher Cd contents contained the
                               major portion of the total Cd in the carbo-
                               nate form  after incubation with soil. In
                               the majority of the sludge-amended soils,
                               more than  60% of the Cd was in the car-
                               bonate form after incubation at both 1/3
                               bar and saturation. In only one case did
                               the proportion of Cd in this fraction fall
                               below 50%. In the Ontario and Escondido
                               sludges, the proportion of Cd in the car-
                               bonate form increased after  incubation
                               with each soil at both moisture contents.
                               A general  increase also occurred in the
                               amount of Cd in the sulfide fraction rela-
                               tive to the  whole sludge following incu-
                               bation  under saturated conditions. The
                               increases in the carbonate and sulfide-
                               bound   fractions  were  made  at  the
                               expense of  organic-bound Cd. Incubation
                               at 1 /3 bar  resulted in appreciably lower

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Table 7. Distribution of Cd in Sludges and Sludge-Amended Soils as Affected by Incubation Water Content (% of total)
Sludge or Soil
and Form of Cd Riatto LA-Composted Cotton Ontario Escondido LA-Liquid Kokomo
Sludge:
Solution
Exchangeable
Adsorbed
Organic
Carbonate
Sulfide

Baywood:
Solution
Exchangeable
Adsorbed
Organic
Carbonate
Sulfide
Delhi:
Solution
Exchangeable
Adsorbed
Organic
Carbonate
Sulfide
Calhi:
Solution
Exchangeable
Adsorbed
Organic
Carbonate
Sulfide
* = None detected.
f = Saturated, 1/3 =
















ND* ND ND NO NO ND ND
0
0
0 0 0 1.1 — 1.1
0000 — 0
66.0 32.0 65.5 36.6 32.8 — 7.0
26.4 50.9 34.5 51.6 53.3 — 81.0
7.6
st

0
0
0
44.6
55.4
0

0
0
0
53.3
46.7
0

0
0
0
54.3
45.7
0

1/3 bar saturation.














17.1 7.3 11.8 12.8 — 10.9
1/3 S 1/3 S 1/3 S 1/3 S 1/3 S 1/3 S 1/3

0.2 0 0 0 0 0 1.8 O 1.4 0 2.2 0 0.1
OOOOOOOOOOOOO
0 0 0 0 0 0 0 O 0 0 0 5.5 3.6
47.7 40.9 16.5 46.8 46.4 15.0 14.8 12.6 20.9 18.4 20.7 19.9 12.0
52.1 59.1 65.3 53.2 53.1 60.0 61.2 59.6 64.2 62.2 57.5 58.2 75.2
0 0 18.2 0 0 25.0 22.0 27.8 13.5 19.4 19.6 16.4 9.1

0 0 0 0 0 0 0.9 O 1.1 0 1.1 0 O.I
OOOOOOOOOOOOO
0 0 0 0 0 0 0 O 0 0 0 6.4 3.9
43.3 39.6 41.8 44.6 43.8 26.5 43.1 23.3 34.5 22.3 56.9 23.2 23.7
56.5 60.4 55.6 55.6 56.2 60.1 51.4 54.7 59.6 60.1 42.0 60.3 70.7
00000 13.4 4.6 22.0 4.8 17.6 0 10.1 1.6

0 0 0 0 0 0 0.5 O 0.3 0 1.0 0 O.2
OOOOOOOOOOOOO
0 0 0 0 0 0 0 0 0 0 0 1.8 2.7
50.0 42.6 44.0 53.5 41.3 14.6 39.0 11.5 19.8 11.7 22.7 5.1 3.8
50.0 57.4 56.0 46.5 58.7 70.6 60.5 61.4 79.9 77.8 65.2 76.2 92.0
00000 14.8 0 27.1 0 10.5 12.1 16.9 1.3
















L J. Lund, G. Sposito, and A. L. Page are with University of California, Riverside,
CA 92521.
J. A. Ryan is the EPA Project Officer (see below).
The complete report, entitled "Determination and Prediction of Chemical Forms of
Trace Metals in Sewage Sludge and Sludge-Amended Soils," (Order No. PB
85-197 1 19/AS; Cost $20.50, subject to change) will be available only from:
National Technical Information Service
5285 Port Royal Road
Springfield, VA 22161
Telephone: 703-487-4650
The EPA Project Officer can be contacted at:
Water Engineering Research Laboratory
U.S. Environmental Protection Agency
Cincinnati, OH 45268
U. S. GOVERNMENT PRINTING OFFICE:1985/559-l 11/20681

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