EPA/600/A-92/079
INCINERATION DATA ON
ARSENIC AND LEAD EMISSIONS
Larry R. Waterland
Acurex Environmental Corporation
555 Clyde Avenue
Mountain View, California 94039-7044
ABSTRACT
Since 1988, nine test programs have been conducted at the Environmental Protection
Agency's Incineration Research Facility aimed at evaluating the fate of trace metals in the rotary
kiln incineration of hazardous wastes and Superfund site materials. Results of six of those test
programs have been reported to date. Of these six, two were parametric test series using a
synthetic hazardous waste formulation and four were incineration treatability test programs using
contaminated Superfund site materials. Results of these six test programs show remarkably
consistent arsenic and lead partitioning behavior among the incinerator system discharge streams.
Overall test programs lead exhibits relatively nonvolatile behavior over a kiln temperature
range from nominally 8l5°C (1,500°F) to 980°C (1,800°F) provided no chlorine is present in the
feed material. Arsenic also exhibits relatively nonvolatile behavior over the same temperature
range regardless of whether the feed contains chlorine at levels up to nominally 8 percent. Arsenic
may be more volatile in the incineration of environmental samples such as Superfund site wastes
than it is from a synthetic waste in which arsenic is introduced as As203 in aqueous solution.
However, even with environmental samples, behavior is relatively nonvolatile. Lead volatility
significantly increases at all kiln temperatures as feed chlorine content increases from 0 to as high
as 8 percent.
INTRODUCTION
In 1988, the EPA's Risk Reduction Engineering Laboratory initiated a research program at
its Incineration Research Facility (IRF) in Jefferson, Arkansas, to investigate the fate of trace
metals fed to a rotary kiln incinerator. The initial test program was a five-test parametric study
of the fate of five hazardous constituent trace metals (arsenic, barium, cadmium, chromium, and
lead) and four nonhazardous constituent trace metals (bismuth, copper, magnesium, and strontium).
In the parametric study each metal's partitioning to the incinerator's discharge streams (kiln ash,
wet scrubber air pollution control system scrubber liquor, and flue gas) was measured, and the
effects of kiln temperature, afterburner temperature, and feed chlorine content on metal
partitioning were evaluated. The parametric tests were performed with a synthetic waste feed
mixture prepared by adding a mixture of organic compounds (toluene, chlorobenzene, and
tetrachloroethene) to a clay-based oil sorbent material, which was screw fed to the incinerator. The
test metals were added by metering a concentrated aqueous solution containing the metal into the
clay/organic mixture in the screw feeder.
The first parametric study, completed in 1988, investigated a venturi scrubber, packed-
column scrubber combination for particulate and acid gas control. A second parametric study,
identical in scope to the first, was completed in 1989. The only difference between the first and
second studies was the air pollution control system (APCS), which was a single-stage ionizing wet
scrubber. Results of the studies were reported in detail in 1991.
1
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A third parametric study was completed in 1991. This study added mercury to the set of test
metals and used a Calvert Force/Flux Condensation scrubber system as the APCS. Results of this
study are only now being evaluated.
Shortly after beginning the trace metal fate research program at the IRF, requests to provide
pilot-scale incineration treatability data to support EPA Regional Office-administered Superfund
site remedial actions began to come to the IRF. Many of the contaminated materials at these sites
contain not only organic contaminants, but hazardous constituent trace metals as well. Thus, key
questions often asked by the Regions concerned the fate of contaminant trace metals, often as
affected by incinerator operation.
As the result of the combination of a series of parametric metals partitioning studies using
synthetic hazardous waste material with a series of Superfund site metals-contaminated materials
tests, the research program at the IRF has generated a substantial body of metals partitioning data
over the past 3 years. Somewhat surprisingly, the metals partitioning data from the wide variety
of feed materials tested has been quite consistent.
This paper looks at the body of arsenic and lead distribution data to give some examples
of the general conclusions that have resulted from metals partitioning research program at the IRF.
Arsenic and lead were chosen for two reasons. They are the most common metal contaminants
in the Superfund site contaminated materials tested at the IRF. In addition, the arsenic behavior
seen is not what might have been expected a few years ago, and the lead partitioning behavior can
be dramatically altered by incineration temperature and waste feed composition.
TEST PROGRAMS
Test Facility
All test programs discussed in this paper were performed in the IRF's rotary kiln incinerator
system (RKS). A process schematic of the RKS is shown in Figure 1. The IRF RKS consists of
a primary combustion chamber, a transition section, and a fired afterburner chamber. After exiting
the afterburner, flue gas flows through a quench section followed by a primary air pollution control
system (APCS). Two primary APCSs are available for use on the unit, as shown in Figure 1. One
consists of a venturi scrubber followed by a packed-column scrubber fabricated by Andersen 2000.
The other is a single-stage ionizing wet scrubber fabricated by Air Plastics, Inc. Downstream of
the primary APCS, a backup secondary APCS, comprised of a demister, an activated-carbon
adsorber, and a high-efficiency particulate (HEPA) filter, is in place. This secondary APCS is
designed to ensure that particulate and organic emissions from the system are acceptable even
under upset conditions.
Test Waste Materials
Results from six different test programs are discussed in this paper. As noted in the
Introduction, two test programs were the parametric trace metal fate programs performed in 1988
and 1989 using a synthetic hazardous waste feed and employing the venturi/packed-column
scrubber for one program and the ionizing wet scrubber for the other. The Introduction also noted
that the synthetic waste feed materials for the parametric test programs was prepared by combining
a mixture of toluene, with varying amounts of chlorobenzene and tetrachloroethene with a clay-
based oil sorbent.
The clay/organic mixture contained nominally 30 percent by weight organic liquids, though
it remained a free-flowing solid. Test trace metals were added to the clay/organic mixture by
metering a concentrated aqueous metals solution onto the clay/organic mixture at the head of the
screw feeder used to feed the synthetic waste to the kiln. Lead in the form of its soluble nitrate
(Pb(N03)2) at 1.6 to 3.2 g/L lead, and arsenic as dissolved As203 also at 1.6 to 3.2 g/L arsenic were
contained in the concentrated aqueous solution.
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SINGLE-STAGE IONIZING
WET SCRUBBER
tXHTj
SCRUBBER
LIQUOR
RECIRCULATION
QUENCH
AFTERBURNER
AIR
NATURAL
LIQUID
AFTERBURNER
SOLIDS
TRANSFER
DUCT
BURNER
VENTuRI
SCRUBBER
NATURAL
GAS,
LIQUID FEED
HOTARY
| DEMISTER
I
I
CARBON BED HEPA
ADSORBER FILTER
PACKED |
Column 1
SCRUBBER
ROTARY KILN
INCINERATOR
SCRUBBER
LIQUOR
RECIRCULATION
MODULAR PRIMARY AIR
POLLUTION CONTROL
SYSTEM DEVICES
REDUNDANT AIR
POLLUTION CONTROL
SYSTEM
o
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Table I. Test feed material arsenic, lead, and chlorine content.
Concentration,
as received/prepared
Test feed
Arsenic,
nig/kg
Lead,
nig/kg
Chlorine,
%
Venturi scrubber parametric test synthetic waste
No chlorine
25
33
0
Low chlorine (average)
24
29
4.0
High chlorine
33
32
8.3
Ionizing wet scrubber parametric test synthetic waste
No chlorine
41
39
0
Low chlorine (average)
51
47
3.5
High chlorine
52
47
6.9
Purity Oil sales site contaminated materials
A layer
5
860
<0.2
B layer
4
10,200
<0.3
C layer
<4
780
<0.2
Baird and McGuire site contaminated soil (average)
85
20
<0.2
New Bedford Harbor site contaminated sediments
(composite)
NA°
236
0.85
Drake Chemical site M-2 soil
16
439
<0.2
'NA = not analyzed.
Test Conditions
The parametric trace metal fate tests were specifically designed to evaluate whether metal
partitioning was affected by incinerator operation and feed composition. The feed composition
variable chosen for evaluation was chlorine content, as noted in Table I. The key incinerator
operating variable chosen was kiln temperature. Similarly, the for Baird and McGuire site soil
tests, EPA Region 2 was interested in whether kiln temperature affected arsenic partitioning, and
for the New Bedford Harbor site sediment tests, the Region was interested in whether kiln
temperature affected PCB destruction and lead partitioning. All three Purity Oil Sales site
materials and the Drake Chemical site soil were tested under a single set of nominal incinerator
operating conditions.
Table II summarizes the incinerator operating conditions for each of the tests. As shown
in the table, kiln temperature variations tested ranged from nominally 815°C (1,500°F) to 980°C
(1,800°F). All tests except the Purity Oil Sales site tests and the New Bedford Harbor site tests
were performed at a nominal afterburner temperature of 1,090°C (2,000°F). The Purity Oil Sales
site tests were performed with nominal afterburner temperature of 980°C (1,800°F) and the New
Bedford Harbor site tests were performed with nominal afterburner temperature of 1,200°C
(2,200°F).
4
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Table II. Incinerator operating conditions.
Kiln exit Afterburner exit
Test
Temperature,
"C (°F)
Flue gas 02,
%
Temperature,
°C (°F)
Flue gas 02,
%
Venturi scrubber parametric tests
Low kiln temperature, low chlorine
825
(1517)
11.9
1071 (1959)
8.4
Moderate kiln temperature
No chlorine
874
(1606)
12.2
1093 (2000)
7.1
Low chlorine
878
(1612)
12.4
1088 (1991)
7.9
Duplicate test
873
(1603)
11.4
1093 (2000)
7.6
High chlorine
870
(1599)
11.4
1092 (1998)
7.4
High kiln temperature, low chlorine
928
(1701)
10.6
1092 (1998)
7.1
Ionizing wet scrubber parametric tests
Low kiJn temperature, low chlorine
819
(1507)
12.3
1095 (2002)
7.7
Moderate kiln temperature
No chlorine
900
(1652)
12.0
1088 (1990)
8.3
Low chlorine
877
(1610)
11.9
1096 (2006)
7.3
Duplicate lest
881
(1618)
12.6
1103 (2018)
7.6
Triplicate test
879
(1615)
12.6
1098 (2008)
8.1
High chlorine
881
(1617)
12.9
1087 (1988)
8.1
High kiln temperature, low chlorine
929
(1704)
11.9
1092 (1998)
7.3
Purity Oil sales site tests
A layer
875
(1607)
12.6
980 (1796)
10.5
B layer
881
(1617)
11.6
984 (1804)
9.9
C layer
827
(1611)
12.3
1001 (1834)
10.0
Baird and McGuire site tests
Low kiJn temperature, low kiln 02
844
(1552)
6.8
1089 (1993)
6.3
Low kiln temperature, high kiln 02
831
(1529)
11.4
1094 (2002)
7.9
Duplicate test
838
(1541)
11.3
1083 (1981)
8.1
High kiln temperature, low kiln 02
994
(1822)
7.5
1099 (2009)
7.3
High kiln temperature, high kiln 02
994
(1822)
10.4
1105 (2021)
7.4
New Bedford Harbor site tests
Low kiln temperature
824
(1516)
11.2
1208 (2206)
6.4
High kiln temperature
984
(1803)
9.0
1208 (2206)
6.0
Duplicate test
985
(1805)
10.0
1208 (2206)
7.0
Drake Chemical site test
Soil M-2
826
(1519)
13.3
1096 (2005)
8.7
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Sampling and Analysis
For all tests, concentrations of the trace metals of interest were measured in the incinerator
feed, the kiln ash discharge, the scrubber liquor, and the scrubber exit flue gas. Flue gas samples
for metals analysis were collected using the multiple metals sampling train described in the
hazardous waste incinerator guidance document (Reference 1) for all tests except the Purity Oil
Sales site tests. An EPA Method 12 sampling train (Reference 2) was used for lead (the only test
flue gas metal of interest) in these tests.
Arsenic and lead analyses of test samples was by inductively coupled argon plasma (ICAP)
spectroscopy (EPA Method 6010, Reference 3) for all tests except arsenic for the Drake Chemical
site tests and both metals for the parametric tests using the venturi/packed-column scrubber.
Graphite furnace atomic absorption (GFAA) spectroscopy methods were used instead for these
exceptions (Method 7060 for arsenic and 7421 for lead.
TEST RESULTS
The measured feed and discharge stream arsenic and lead concentrations can be combined
with measured feed and discharge flowrates, and the fraction of both metals fed accounted for the
respective discharges can be calculated. The sum of these discharge fractions represents the mass
balance closure for each metal in each test. Ideally, near 100 percent trace metal mass balance
closure would be desirable. However, past experience in tests to determine the distribution of trace
metals from combustion sources has shown that typical good results are in the 30 to 200 percent
range. For the tests discussed in this paper, lead mass balance closures range from 8 to
177 percent and averaged 92 percent. Arsenic closures ranged from 32 to 101 percent and
averaged 67 percent.
Given that variable and less than perfect mass balance closure is invariably experienced, it
is difficult to draw conclusions regarding the affect of incinerator operation or feed characteristics
on metal partitioning using only percent-of-feed fractional distributions. However, a clearer picture
of the variation in relative metal distributions is possible when percent-of-feed fractional
distributions are normalized by the total mass balance closure achieved. These normalized, or
percent-of-measured fractions represent fractions that would have resulted had mass balance
closure in each case been 100 percent. Use of distribution fractions normalized in this manner
allows clearer data interpretation, because variable mass balance closure is removed as a source
of test-to-test data variability. The use of normalized distributions represents a best attempt to
quantify metal partitioning phenomena, given variable and less than perfect mass balance closure.
Table III summarizes the normalized distribution fraction of arsenic and lead measured in
each of the tests listed in Table II. For completeness, the total mass balance closure achieved for
each metal (ratio of the sum of amount of each metal measured in the discharges to the amount
of metal fed to the incinerator) is also shown in Table III for each test.
The test condition data given in Table II show that over the six test programs performed,
kiln temperature was varied over four nominal levels: 815°C (1,500°F), 870°C (1,600°F), 925°C
(1,700°C), and 980°C (1,800°F). The feed composition data in Table I show that feed chlorine
content also varied over four nominal levels; no chlorine, 1 percent, 4 percent, and 8 percent.
Figure 2 plots the normalized lead kiln ash fraction data from Table III in bar chart form
for all the tests with no feed chlorine. For the purpose of the Figure 2 plot, the three Baird and
McGuire site tests at the low kiln temperature and the two tests at the high kiln temperature were
considered replicates. This presumes that the kiln exit flue gas 02 variations tested had no effect
on metal partitioning. This clearly appears to be the case for the lead distribution data in
Table III. For these replicates, the height of the bar in Figure 2 represents the average of the
replicate fractions. The range of normalized fractions measured over the replicates is shown by
the "error bar" superimposed in the figure.
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Table 111. Normalized arsenic and lead discharge distributions.
Normalized distribution, % of metal measured
Arsenic
Lead
Test
Kiln ash
Scrubber
liquor
Scrubber
exit llue gas
Mass balance
closure
achieved
Kiln ash
Scrubber
liquor
Scrubber
exit Flue gas
Mass balance
closure
achieved
Venturi scrubber parametric tests
Low kiln temperature, low chlorine
94
3
76
13
37
50
90
Moderate kiln temperature
No chlorine
94
4
2
68
84
5
11
8
Low chlorine
86
8
6
46
15
36
49
84
Duplicate test
92
4
4
39
14
36
50
37
High chlorine
92
3
5
52
6
20
74
96
High kiln temperature, low chlorine
84
8
8
49
11
22
67
77
Ionizing wet scrubber parametric tests
Low kiln temperature, low chlorine
92
3
5
64
91
1
8
130
Moderate kiln temperature
No chlorine
89
4
7
66
90
1
9
47
Low chlorine
80
9
11
47
81
7
12
136
Duplicate test
90
4
6
62
82
5
13
94
Triplicate test
89
5
6
77
85
4
11
102
High chlorine
95
3
2
65
83
10
7
95
High kiln temperature, low chlorine
82
11
7
95
71
14
15
177
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Table III. Normalized arsenic and lead discharge distributions (concluded).
Normalized distribution, % of metal measured
Test
Arsenic
Lead
Kiln ash
Scrubber
liquor
Scrubber
exit llue gas
Mass balance
closure
achieved
Kiln ash
Scrubber Scrubber
liquor exit flue gas
Mass balance
closure
achieved
Purity Oil sales site tests
A layer
94
1
5
155
B layer
91
2
7
126
C layer
96
1
3
169
Baird and McGuire site tests
Low kiln temperature, low 02
76
22
2
101
93
3
4
148
Low kiln temperature, high 02
72
23
5
82
89
4
7
113
Duplicate test
66
29
5
74
91
3
6
98
High kiln temperature, low 02
56
38
6
78
69
13
18
51
High kiln temperature, high O,
36
55
9
62
69
12
19
37
New Bedford Harbor site tests
Low kiln temperature
53
30
17
66
High kiln temperature
23
35
42
38
Duplicate test
19
26
55
54
Drake Chemical site tests
Soil M-2
>77
<8
15
73
90
8
2
73
oo
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100
60
ESD 067-92
C 60
40
20
I
I
815°C
Vs.
'A
I
i
T
870°C 925°C
KILN TEMPERATURE
t^SSSS^ Baird & McGuire
Drake M-2
\///\ Parametric Ionizing
Parametric Venturi
Purify A Layer
NWl Purify B Layer
Purify C Layer
980°C
Figure 2. Normalized kiln ash fractions for lead; tests with no feed chlorine.
The data in Figure 2 show that lead was relatively nonvolatile at a kiln temperature of
nominally 815°C (1,500°F). For the two different Superfund site materials tested at this nominal
temperature, about 90 percent of the lead discharge was accounted for in the kiln ash.
Similar kiln ash fractions were measured for the five materials tested at a nominal kiln
temperature of 870°C (1,600°F). However, lead became much more volatile at a nominal kiln
temperature of 980°C (1,800°F). At this temperature for the Baird and McGuire soil, the kiln ash
accounted for a significantly reduced fraction, about 70 percent of the lead discharged.
Similar behavior is seen in Figure 3, which is a bar chart plot of the ionizing wet scrubber
parametric test data at low feed (4 percent) chlorine content and the New Bedford Harbor data
(sediments contained roughly 1 percent chlorine). For the nominal 870°C (1,600°F) ionizing wet
scrubber test conditions, the height of the bar represents the average of the three replicate test kiln
ash fractions from Table III. The kiln ash fraction range over the three replicate tests is shown by
the superimposed error bar.
Figure 3 shows a steady increase in lead volatility as measured by steady decrease in lead
kiln ash fraction over the nominal 815° to 925°C (1,500° to 1,700°F) range for the ionizing wet
scrubber parametric tests. Lead exhibited significantly more volatile behavior in the New Bedford
Harbor sediment tests. Only about 50 percent of the lead discharged was accounted for in the kiln
ash for the test at nominal kiln temperature of 815°C (1,500°F). The kiln ash fraction decreased
to about 20 percent at the higher kiln temperature of nominally 980°C (1,800°F).
Arsenic shows similar behavior as illustrated in Figure 4 which is a bar chart plot of arsenic
kiln ash fractions for all tests with arsenic present in the feed. For both sets of synthetic waste
parametric tests, arsenic kiln ash fractions steadily decreased from just over 90 percent at a nominal
815°C (1,500°F) kiln temperature to just at 90 percent at a nominal 860°C (1,600°F) kiln
temperature, to just under 85 percent at a nominal 925°C (1,700°F) kiln temperature. Arsenic was
9
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100
ESD 068-92
80 -
60 -
1
to
<
2 40
20 -
I
1ZL
V//I Parametric Ionizing
New Bedford Harbor
T
815°C
870°C 925°C
KILN TEMPERATURE
980°C
Figure 3. Normalized kiln ash fractions for lead; tests with low (1 to 4 percent) feed chlorine.
100
80
Q 60
~—
o
<
CE
LL
| 40
2
ESD 069-92
20 -
53
I
Ipl
815°C
i
870°C 925°C
KILN TEMPERATURE
Baird & McGuire
^¦1 Drake M-2
\//A Parametric Ionizing
I I Parametric Venturi
IS
|
980°C
Figure 4. Normalized kiln ash fractions for arsenic.
10
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more volatile at 815°C (1,500°F) from the Drake Chemical site soil, and even more volatile at this
temperature from the Baird and McGuire site soil. However, the kiln ash still accounted for just
over 70 percent of the arsenic discharged. Arsenic exhibited significantly more volatile behavior
from the Baird and McGuire soil at the high kiln temperature condition of about 980°C (1,800°F).
However, even at this temperature the kiln ash still accounted for just under half the arsenic
discharged.
The effect of feed chlorine content on lead volatility is shown in Figure 5. For all tests in
the base discussed in this paper, the presence of even a small amount of feed chlorine (i.e.,
1 percent) caused a significant increase in lead volatility as measured by a decrease in normalized
lead kiln ash fraction. The parametric tests with synthetic waste at a nominal kiln temperature of
870°C (1,600°F) show a decrease in lead kiln ash fraction as feed chlorine content is increased
from 0 to nominally 4 and 8 percent. The venturi scrubber parametric test data show a dramatic
increase in lead volatility with increasing feed chlorine content. The ionizing wet scrubber
parametric show a less prominent volatility increase with increased feed chlorine content to
4 percent, but a definite one nonetheless.
Even the data from three Superfund site materials tests supports the observation that the
presence of feed chlorine increases the volatility of lead. Lead was relatively nonvolatile from both
the Drake Chemical site M-2 soil and the Baird and McGuire site soil tested at a kiln temperature
of nominally 815°C (1,500°F). However, lead was significantly more volatile from the New
Bedford Harbor sediments, which contained about 1 percent chlorine, at this temperature. The
same relative behavior is seen for the Baird and McGuire site and New Bedford Harbor site tests
at a kiln temperature of nominally 980°C (1,800°F).
CONCLUSIONS
The results from six test programs completed at EPA's IRF over the past three years show
remarkably consistent partitioning behavior of arsenic and lead in rotary kiln incinerator discharge
streams. This consistent behavior exists over a range of test feed materials from a synthetic clay-
based sorbent material through contaminated soils, sludges, and marine sediments from four
Superfund sites. Over all these tests:
• Lead exhibits relatively nonvolatile behavior over a kiln temperature range from
nominally 815°C (1,500°F) to 980°C (1,800°F) provided no chlorine is present in the
feed material. The kiln ash discharge accounts for about 90 percent of the lead
measured in the discharge streams at kiln temperatures of 815°C and 870°C (1,500°
and 1,600°F), decreasing to about 70 percent at a kiln temperature of 980°C (1,800°F).
• Arsenic exhibits relatively nonvolatile behavior over the same temperature range
regardless of whether the feed contains chlorine at levels up to nominally 8 percent.
For a synthetic waste feed which incorporates arsenic as As203 in aqueous solution, the
kiln ash accounts for just over 90 percent of the arsenic measured in incinerator
discharges at a kiln temperature of 815°C (1,500°F), decreasing to just under
85 percent at a kiln temperature of 925°C (1,700°F).
• Arsenic may be more volatile in the incineration of environmental samples such as
Superfund site wastes. However, overall behavior is still relatively nonvolatile, the kiln
ash accounted for at least 70 percent of the arsenic discharged in the incineration of
Superfund site materials at a kiln temperature of 815°C (1,500°F) decreasing to just
under 50 percent at a kiln temperature of 980°C (1,800°F).
• Lead volatility is significantly increased with chlorine present in the incinerator feed,
with increased volatility exhibited as feed chlorine content progressively increases from
0 to 8 percent.
11
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100
BO
60
40
20
ESD 070-92
815°C
870°C 925°C
KILN TEMPERATURE
FACE
VT7\
Baird & McGuire
Drake M-2
Parametric Ionizing
Parametric Venturi
New Bedford Harbor
No C
1% C
4% CI
8% CI
980°C
Figure 5. Normalized kiln ash Tractions for lead; effect of feed chlorine.
REFERENCES
1. "Proposed Methods for Stack Emissions Measurement for CO, 02, THC, HC1, and Metals at
Hazardous Waste Incinerators," U.S. Environmental Protection Agency, Office of Solid Waste,
November 1989.
2. 40 CFR, Part 60, Appendix A.
3. 'Test Methods for Evaluating Solid Waste: Physical/Chemical Methods," EPA SW-846, 3rd
edition, November 1986.
NOTICE
The information described in this paper has been funded wholly or in part by the U.S.
Environmental Protection Agency under Contract 68-C-0038 to Acurex Corporation. It has been
subjected to the Agency's peer and administrative review and approved for presentation and
publication.
12
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TECHNICAL REPORT DATA
(Please read Instructions on the reverie before compleii
1. REPORT NO. 2.
EPA/600/A-92/079
3
4. TITLE AND SUBTITLE
Incineration Data on Arsenic and Lead Emissions
8. report date
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
Larry R. Waterland, Acurex Environmental Corporation
B. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Acurex Environmental Corporation
555 Clyde Avenue
Mountain View, California 94039
10 PROGRAM ELEMENT NO.
11. CONTRACT/GRANT NO.
68-C9-0038
12. SPONSORING AGENCY NAME ANO ADDRESS
Risk Reduction ENgineering Laboratory--Cin"., OH
Office of Research and Development
U.S. Environmental Protection Agency
Cincinnati, Ohio 45268
13. TYPE OF RE PORTAND PERIOD COVERED
Proceedi nqs
14. sponsoring agency code
EPA/600/14
15. SUPPLEMENTARY NOTES
Project Officer: Robert E. Mournighan 513-569-7430
16. ABSTRACT
Since 1988, nine test programs have been conducted at the Environmental Protection Agency
Incineration Research Facility aimed at evaluating the fate of trace metals in the
rotary kiln incineration of hazardous wastes and Superfund site materials. Results of
six of those test programs have been reported to date. Of these six, two were
parametric test series using a synthetic hazardous waste formulation and four were
incineration treatability test programs using contaminated Superfund site materials.
Results of these six text programs show remarkably consistent arsenic and lead
partitioning behavior among the incinerator system discharge streams.
Overall test programs lead exhibits relativley nonvolatile, behavior over a kiln
temperature range from nominally 815^C (1 ,500 F) to 980®rC(l ,800F) provided no chlorine \
is present in the feed material. Arsenic also exhibits relatively nonvolatile behavior -
over the same temperature range reagardless of whether the feed contains chlorine at
levels up to nominally 8 percent. Arsenic may be more volatile in the incineration of
environmental samples such as Superfund site wastes than it is from a synthetic waste
in which arsenic is introduced as A^O^in aqueous solution. However, even with
environmental samples, behavior is relatively nonvolatile. Lead volatility significantly
increases at all kiln temperatures as feed chlorine content increases from 0 to as high
as 8 percent.
17. KEY WORDS AND DOCUMENT ANALYSIS
a. descriptors
b.identifiers/open ended terms
c. COSati Field/Group
arsenic
incineration
ie. distribution statement
Release to public
19. SECURITY class (This Report)
UNCLASSIFIED
2i. no. of pages
13
20. security Class (This page/
UNCLASSIFIED
22 PRICE
EPA Form 2220-1 (R«». 4-77) previous edition is obiolete
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