PUBLIC HEALTH ASSESSMENT
USA DEFENSE DEPOT MEMPHIS
MEMPHIS, SHELBY COUNTY, TENNESSEE
APPENDICES
APPENDIX A - PARAMETERS TESTED IN THE SCREENING, 1989
AND 1995-1998 REMEDIAL, BACKGROUND,
AND BRAC SAMPLING PROGRAMS
Parameters Tested in the Screening Sites, 1989 and 1995-1998 Remedial,
Background, and BRAC Sampling Programs23
1-methyl naphthalene
1-bromo-4-fluorobenzene
4-bromofluorobenzene
1,1-dichloroethane
1,1-dichloroethene
1,1,1-trichloroethane
1,1,2-trichloroethane
1,1,2,2-tetrachloroethane
1,2-dichloroethane
1,2-dichloropropane
1,2-dichloroethene (total)
1,2,3,4,6,7,8-heptachlorodibenzofuran
1,2,3,4,6,7,8-heptachlorodibenzo-p-dioxin
1,2,3,4,7,8-hexachlorodibenzo-p-dioxin
1,2,3,4,7,8-hexachlorodibenzofuran
1,2,3,4,7,8,9-heptachlorodibenzofuran
1,2,3,6,7,8-hexachlorodibenzofuran
1,2,3,6,7,8-hexachlorodibenzo-p-dioxin
1,2,3,7,8-pentachlorodibenzofuran
1,2,3,7,8-pentachlorodibenzo-p-dioxin
1,2,3,7,8,9-hexachlorodibenzo-p-dioxin
1,2,3,7,8,9-hexachlorodibenzofuran
1,2,4-trichlorobenzene
1,3-dichlorobenzene
1,4-dichlorobenzene
2-chlorophenol
2-fluorobiphenyl - ss
2-nitrophenol
2-butanone
2-nitroaniline
2-methylphenol
2-methyl naphthalene
2-hexanone
2-fluorophenol - ss
2-chloronaphthalene
2-chlorophenol
2,2'-oxybis(1-chloropropane)
2,3,4,6,7,8-hexachlorodibenzofuran
2,3,4,7,8-pentachlorodibenzofuran
2,3,7,8-tetrachlorodibenzofuran
2,3,7,8-tetrachlorodibenzo-p-dioxin
2,4-dimethylphenol
2,4-dinitrophenol
2,4 DB
2,4-dichlorophenol
2,4-dinitrotoluene
2,4-dichlorophenylacetic acid - ss
2,4-DP (dichloroprop)
2,4-D
2,4,5-T
2,4,5-trichlorophenol
2,4,6-tribromophenol - ss
2,6-dinitrotoluene
3-nitroaniline
3,3'-dichlorobenzidine
4-chloroaniline
4-bromophenyl-phenylether
4-nitroaniline
4-methylphenol
4-chlorophenyl-phenylether
4-chloro-3-methylphenol
4-chlorophenyl-phenylether
4-methyl-2-pentanone
4-nitrophenol
4,6-dinitro-2-methylphenol
acenaphthene
acenaphthylene
acetone
aldrin
alpha-chlordane
alpha BHC
alpha endosulfan
aluminum
aluminum, dissolved
anthracene
antimony, dissolved
antimony
arsenic, dissolved
arsenic
barium, dissolved
barium
benzene
benzo(a)anthracene
benzo(a)pyrene
benzo(b)fluoranthene
benzo(g,h,i)perylene
benzo(k)fluoranthene
benzoic acid
benzyl butyl phthalate
benzyl alcohol
beryllium, dissolved
beryllium
beta endosulfan
beta BHC
bis(2-chloroethoxy)methane
bis(2-chloroethyl)ether
bis(2-ethylhexyl)phthalate
bromodichloromethane
bromofluorobenzene - SS
bromoform
bromomethane
butyl benzyl phthalate
cadmium
cadmium, dissolved
calcium
calcium, dissolved
carbon disulfide
carbon tetrachloride
chlordane
chlorobenzene
chloroethane
chloroform
chloromethane
chromium |
chromium, dissolved
chrysene
cis-1,3-dichloropropene
cobalt
cobalt, dissolved
copper
copper, dissolved
dalapon
DDD
DDE
DDT
decachlorobiphenyl - ss
delta BHC
di-n-butyl phthalate
di-n-octylphthalate
dibenz(a,h)anthracene
dibenzofuran
dibromochloromethane
dibromofluoromethane
dicamba
dichloroprop
dieldrin
diethyl phthalate
dimethyl phthalate
dinoseb
endosulfan II
endosulfan sulfate
endosulfan I
endrin ketone
endrin aldehyde
endrin
ethyl benzene
fluoranthene
fluorene
fluoride, free
fluorobenzene gamma BHC (lindane)
gamma-chlordane
heptachlor
heptachlor epoxide
hexachlorobenzene
hexachlorobutadiene
hexachlorocyclopentadiene
hexachloroethane
indeno(1,2,3-cd)pyrene
iron
iron, dissolved
isophorone
lead
lead, dissolved
magnesium
magnesium, dissolved
manganese
manganese, dissolved
MCPP
mercury
mercury, dissolved
methoxychlor
methyl isobutyl ketone
methyl ethyl ketone (2-butanone)
methylene chloride
n-nitrosodiphenylamine
n-nitroso-di-n-propylamine
naphthalene
nickel, dissolved
nickel
nitrobenzene
octachlorodibenzo-p-dioxin
octachlorodibenzofuran
PCB, total
PCB-1016 (arochlor 1016)
PCB-1221 (arochlor 1221)
PCB-1232 (arochlor 1232)
PCB-1242 (arochlor 1242)
PCB-1248 (arochlor 1248)
PCB-1254 (arochlor 1254)
PCB-1260 (arochlor 1260)
pentachlorophenol
petroleum hydrocarbons
pH
phenanthrene
phenol
potassium, dissolved
potassium
pyrene
selenium
selenium, dissolved
silver
silver, dissolved
silvex (2,4,5-TP)
sodium, dissolved
sodium
styrene
TCDD equivalence
terphenyl-d14
tert-butyl methyl ether
tetrachloro-m-xylene - ss
tetrachloroethylene (PCE)
thallium
thallium, dissolved
toluene
total PAHs
total xylenes
total fuel hydrocarbon, gasoline
total 1,2-dichloroethene
total organic carbon (soil/water)
toxaphene
trans-1,3-dichloropropene
trichloroethylene (TCE)
vanadium, dissolved
vanadium
zinc
zinc, dissolved |
APPENDIX B - EXPLANATION OF EVALUATION PROCESS
In evaluating these data, ATSDR used comparison values to determine which chemicals to
examine more closely. Comparison values are health-based thresholds below which no known
or anticipated adverse human health effects occur. Comparison values can be based on cancer
or non-cancer health effects. Non-cancer levels are based on the lowest (i.e., most toxic) valid
toxicologic study for a chemical and the assumption that a small child (22 lbs.) is exposed
every day. Cancer levels are the media concentrations at which there would be a one in a
million excess cancer risk for an adult eating contaminated soil every day for 70 years. For
chemicals for which both cancer and non-cancer numbers exist, the more toxic (i.e., lower)
level is used. A description of the comparison values used in this evaluation can be found in
Appendix C. Exceeding a comparison value does not mean that health effects will occur, just
that more evaluation is needed.
Further evaluation focuses on identifying which chemicals and exposure situations are likely to
be a health hazard. The first step is the calculation of child and adult exposure doses, as
described in Appendix D. These are then compared with an appropriate health guideline for a
chemical. An exposure dose is the amount of chemical ingested daily per unit of body weight.
Health guidelines are the amount of chemical per unit of body weight where health effects very
likely do not occur, based on investigations of human exposures to the chemical, or, if human
data don't exist or are not valid, of animal experiments. Most health guidelines are based on
animal data. The results of these calculations are presented in Tables D1 and D2 starting on
page 67. Any exposure situation, where the exposure dose is lower than a health guideline, is
eliminated from further evaluation.
The next step in the evaluation process is determining whether the worst case exposure
situations used in earlier calculations need to be revised to better fit the actual situation. For
example, both Dunn Field and the DDMT Main Facility have reportedly been fenced and
guarded since the Depot opened. Except for the area near the 8 base housing units, small
children could not have experienced health effects due to exposure to contaminants on-site
because they could not enter the site. Thus, exposure situations involving small children (1-2
years old) were dropped from further evaluation except for those that include the base housing
area on Main Facility. Likewise, exposure situations for adults on Dunn Field would assume
that exposure is less frequent than for adults on the Main Facility because it appears that no
one spent every work day on Dunn Field.
The last evaluation step is the comparison of these revised exposure doses with known
toxicological values for the chemical of concern. This would include the no observed and
lowest observed adverse health effects levels (NOAEL & LOAEL) identified in ATSDR
Toxicological Profiles. If the chemical of concern is a carcinogen, the cancer risk is
recalculated using the revised exposure dose. These comparisons are the basis for stating
whether the exposure might be a health hazard.
APPENDIX C - EXPLANATION OF COMPARISON VALUES
Health Comparison Values
Health Comparison Values (CVs) are the contaminant concentrations found in a specific
media (air, soil, or water) and used to select contaminants for further evaluation. The CVs
used in this document are listed below.
Environmental Media Evaluation Guides (EMEGs) are estimated contaminant
concentrations in a media where no chance exists for non-carcinogenic health effects to occur.
The EMEG is derived from U.S. Agency for Toxic Substances and Disease Registry's
(ATSDR) minimal risk level (MRL).
Remedial Media Evaluation Guides (RMEGs) are estimated contaminant concentrations in a
media where no chance exists for non-carcinogenic health effects to occur. The RMEG is derived from U.S. Environmental Protection Agency's (EPA) reference dose (RfD).
Cancer Risk Evaluation Guides (CREGs) are estimated contaminant concentrations that
would be expected to cause no more than one additional excess cancer in a million persons
exposed over a lifetime. CREGs are calculated from EPA's cancer slope factors (CSF).
Risk-Based Concentrations (RBCs) are the estimated contaminant concentrations in which no
chance exists for carcinogenic or noncarcinogenic health effects. The RBCs used in this public
health assessment were derived using provisional reference doses or cancer slope factors
calculated by toxicologists of EPA's Region III (92).
EPA Action Levels (EPA ALs) are the estimated contaminant concentrations in water of
which additional evaluation is needed to determine whether action is required to eliminate or
reduce exposure. Action levels can be based on mathematical models.
EPA Soil Screening Levels (EPA SSL) are estimated contaminant concentrations in soil at which additional evaluation is needed to determine if action is required to eliminate or reduce exposure.
APPENDIX D - CALCULATION OF ESTIMATED EXPOSURE DOSES
Calculation of Exposure Dose from Ingestion of Contaminated Soil
The exposure doses for ingestion of contaminated soil were calculated in the following manner.
The maximum or mean concentration for a chemical in DDMT soil was multiplied by the soil
ingestion rate for adults, 0.0001 Kg/day, or the rate for children, 0.0002 Kg/day. This
product was divided by the average weight for an adult, 70 Kg (154 pounds), or for a small
child, 10 Kg (22 pounds). For adults, we assumed that only DDMT workers could have been
exposed. Thus, exposure could have occurred 5 times a week rather than 7, which resulted in
the exposure dose being adjusted by a factor of 5/7ths (0.7). Exposure doses for children were
calculated only for exposure situations near the 8 base housing units on the Eastern edge of the
main facility. Children, especially small children, could not likely be exposed elsewhere on
the DDMT Main Facility and Dunn Field because they reportedly have always been fenced and
guarded. Those calculations assume frequent daily exposure to soil contaminated at the
specified level. The results of the actual calculations are recorded in Tables D1 - D2 on the
following pages.
Calculation of Risk of Carcinogenic Effects
Carcinogenic risks from the ingestion of soil were calculated using the following procedure.
The adult exposure doses for ingestion of soil were calculated as described previously, then
multiplied by the EPA's Cancer Slope Factor (CSF) for that chemical (93). This result was
multiplied by 0.4 because maximum exposure length of 30 years was assumed rather than the
70 years assumed for the CSF. This is because we concluded that only workers could be
exposed. Results of the calculation of carcinogenic risk from exposure can be found on Tables D1 and D2 on the following pages.
The actual risk of cancer is probably lower than the calculated number. The method used to
calculate EPA's Cancer Slope Factor assumes that high dose animal data can be used to
estimate the risk for low dose exposures in humans (94). The method also assumes that there
is no safe level for exposure (95). Little experimental evidence exists to confirm or refute
those two assumptions. Lastly, the method computes the 95% upper bound for the risk, rather
than the average risk, which results in there being a very good chance that the risk is actually
lower, perhaps several orders of magnitude (96). One order of magnitude is 10 times greater
or lower than the original number, two orders of magnitude are 100 times, and three orders are 1,000 times.
Table D1 - Estimated Exposure
Doses and Cancer Risk for Dunn Field Soil Contaminants
Compared to Health Guidelines for Ingestion1 |
| Contaminant |
Maximum Level in parts per million
(ppm) |
Estimated Adult Exposure Doses
in mg/kg/day* |
Health Guideline in mg/kg/day* |
Source of Guideline |
Cancer Risk |
| Arsenic |
35 |
0.00004 |
0.0003 |
MRL2 |
2 in 100,0003 |
| Alpha-chlordane |
1.5 |
0.000002 |
0.0003 |
MRL2 |
1 in 1,000,0004 |
| Dieldrin |
0.5 |
0.000001 |
0.00005 |
MRL2 |
1 in 100,0003 |
| Benzo(a)pyrene5 |
68 |
0.00007 |
none |
none |
2 in 10,0006 |
* mg/kg/day = milligrams/kilogram/day
1 An explanation of how these exposure doses and
cancer risk were calculated can be found in the preceding page. No health
guidelines are available for lead, benzo(a)anthracene, benzo(b)fluoranthene,
indeno(1,2,3-c,d)pyrene, benzo(k)fluoranthene, and dibenz(a,h)anthracene.
2 MRL = ATSDR's minimal risk level. For more information
on the MRL for arsenic or alpha- chlordane, see the arsenic or chlordane
toxicological profiles.
3 Maximum additional lifetime risk of cancer per
100,000 individuals.
4 Maximum additional lifetime risk of cancer per
1,000,000 individuals.
5 Maximum additional lifetime risk of cancer per
10,000 individuals. |
Table D2 - Estimated Exposure
Doses and Cancer Risk for Soil Contaminants
Compared to Health Guidelines for Ingestion1 |
| Contaminant |
Level in Parts per Million (ppm) |
Estimated Adult Exposure Doses
in mg/kg/day* |
Health Guideline in mg/kg/day* |
Source of Guideline |
Cancer Risk |
| Maximum Arsenic Level |
84 |
0.0001 |
0.0003 |
MRL2 |
2 in 10,0003 |
| Mean Arsenic Level |
15.7 |
0.00002 |
0.0003 |
MRL2 |
3 in 100,004 |
| Maximum Benzo(a)Pyrene |
450 |
0.00007 |
none |
none |
5 in 1,0005 |
| Mean Benzo(a)Pyrene Level |
6.6 |
0.000009 |
none |
none |
7 in 100,004 |
| Maximum Beryllium Level |
2 |
0.000003 |
0.002 |
RfD6 |
1 in 100,0004 |
| Mean Beryllium Level |
0.3 |
0.0000004 |
0.002 |
RfD6 |
2 in 1,000,0007 |
| Maximum Dieldrin Level |
10 |
0.00001 |
0.00005 |
MRL2 |
2 in 100,0004 |
| Mean Dieldrin Level |
0.5 |
0.0000007 |
0.00005 |
MRL2 |
1 in 1,000,0007 |
| Maximum DDT Level |
59 |
0.00008 |
0.0005 |
RfD6 |
3 in 100,0004 |
| Mean DDT Level |
0.8 |
0.0000008 |
0.0005 |
RfD6 |
0.4 in 1,000,0007 |
* mg/kg/day = milligrams/kilogram/day
1 An explanation of how these exposure doses and
cancer risk were calculated can be found in the preceding page. No health
guidelines are available for lead, benzo(a)anthracene, benzo(b)fluoranthene,
indeno(1,2,3-c,d)pyrene, and dibenz(a,h)anthracene.
2 MRL = ATSDR's minimal risk level.
3 Maximum additional lifetime risk of cancer per
10,000 individuals.
4 Maximum additional lifetime risk of cancer per
100,000 individuals.
5 Maximum additional lifetime risk of cancer per
1,000 individuals.
6 RfD = EPA's reference dose.
7 Maximum additional lifetime risk of cancer per
1,000,000 individuals. |
APPENDIX E - CONTAMINANT TABLES FOR
THE DEFENSE DEPOT - MEMPHIS, TENNESSEE
Table E1 - Contaminants above Comparison Value in Dunn Field Sediment*
| Contaminant |
Range in Soil
in mg/kg1 |
Dunn Field Mean in
mg/kg |
Background Mean in
mg/kg |
Samples > DL2 |
Samples >CV3 |
CV in mg/kg |
CV Source4 |
| Beryllium |
ND - 1.2 |
0.8 |
0.2 |
11/12 |
11/05 |
0.2/3006 |
CREG/RMEG |
| Benzo(a)pyrene |
ND - 4.1 |
1.0 |
0.9 |
11/12 |
7 |
0.1 |
CREG |
| Benzo(b)fluoranthene |
0.1 -4.9 |
1.5 |
0.9 |
12/12 |
7 |
0.9 |
EPA SSL |
| Dibenz(a,h)anthracene |
ND - 0.5 |
0.2 |
0.8 |
7/12 |
6 |
0.09 |
EPA SSL |
| Benzo(a)anthracene |
0.07 - 3.8 |
0.9 |
0.9 |
12/12 |
3 |
0.9 |
EPA SSL |
| Indeno(1,2,3-c,d)pyrene |
ND - 3.2 |
0.8 |
0.8 |
9/12 |
2 |
0.9 |
EPA SSL |
* The source of these data is the 1990 RI
(3), and the 1995 sediment sampling data provided directly to ATSDR by DDMT.
There is a legend for this table following Table E7. |
Table E2 - Contaminants Detected in Dunn Field Surface Water*
| Contaminant |
Range in Water in mg/L7 |
Samples > DL2 |
Samples > CV3 |
CV in mg/L** |
CV Source4 |
| Acetone |
0.002 - 0.02 |
3/3 |
0 |
10 |
RMEG |
| Barium |
0.06 - 0.09 |
3/3 |
0 |
70 |
RMEG |
| Benzoic Acid |
ND - 0.003 |
1/3 |
0 |
4,000 |
RMEG |
| Bis(2-ethylhexyl)phthalate |
ND - 0.01 |
1/3 |
0 |
0.3/206 |
CREG/RMEG |
| Cadmium |
ND - 0.006 |
1/3 |
0 |
0.2 |
EMEG |
| Copper |
ND - 0.02 |
2/3 |
0 |
130 |
EPA Action Level |
| Dieldrin |
ND - 0.0001 |
2/3 |
0 |
0.0002/0.056 |
CREG/EMEG |
| Lead |
ND - 0.04 |
1/3 |
0 |
1.5 |
EPA Action Level |
| Methylene Chloride |
ND - 0.001 |
1/3 |
0 |
0.5/606 |
CREG/EMEG |
| Nitrosodiphenylamine |
ND - 0.005 |
1/3 |
0 |
0.7 |
CREG |
| Zinc |
0.06 - 0.1 |
3/3 |
0 |
300 |
EMEG |
* The source of these data is the 1990 RI
(3), and the 1995 sediment sampling data provided directly to ATSDR by DDMT.
** These comparison values are multiplied by 100
because it is assumed that daily ingestion of surface water for a small
child is 10 milliliters (ml) rather than the 1 liter (1,000 ml) used for
drinking tap water.
There is a legend for this table following Table E7. |
Table E3 - Surface Soil Contaminants above a Comparison Value
| Contaminant |
Range in mg/kg1 |
Samples > DL2 |
Samples > CV3 |
CV in mg/kg |
CV Source4 |
| Alpha-chlordane |
ND - 4 |
50/243 |
5/15 |
0.5/36 |
CREG/RMEG |
| Antimony |
ND - 2,420 |
114/323 |
8 |
20 |
RMEG |
| Arsenic |
ND - 101 |
352/361 |
351/705 |
0.5/206 |
CREG/EMEG |
| Barium |
6 - 7,300 |
158/158 |
3 |
4000 |
RMEG |
| Benzo(a)anthracene |
ND - 970 |
167/352 |
59 |
0.9 |
EPA SSL |
| Benzo(a)pyrene |
ND - 450 |
164/349 |
121 |
0.1 |
CREG |
| Benzo(b)fluoranthene |
ND - 540 |
174/359 |
59 |
0.9 |
EPA SSL |
| Benzo(k)fluoranthene |
ND - 450 |
151/338 |
23 |
9 |
EPA SSL |
| Beryllium |
ND - 2 |
162/319 |
142/05 |
0.2/3006 |
CREG/RMEG |
| Beta BHC |
ND - 2.5 |
11/168 |
2 |
0.4 |
CREG |
| Bis(2-ethylhexyl) phthalate |
ND - 250 |
45/110 |
1/05 |
50/1,0006 |
CREG/RMEG |
| Cadmium |
ND - 159 |
187/347 |
6 |
10 |
EMEG |
| Chlordane |
ND - 1.2 |
9/66 |
1/05 |
0.5/306 |
CREG/EMEG |
| Chromium |
5 - 16,200 |
370/370 |
17 |
300 |
RMEG |
| Chrysene |
ND - 620 |
178/357 |
2 |
88 |
EPA SSL |
| Copper |
ND - 28,500 |
370/372 |
2 |
3,100 |
HEAST |
| DDD |
ND - 3.6 |
116/316 |
1 |
3 |
CREG |
| DDE |
ND - 39 |
187/333 |
9 |
2 |
CREG |
| DDT |
ND - 59 |
205/334 |
15/15 |
2/306 |
CREG/RMEG |
| Dibenz(a,h)anthracene |
ND - 160 |
21/334 |
15 |
0.09 |
EPA SSL |
| Dieldrin |
ND - 10 |
180/324 |
125/95 |
0.04/36 |
CREG/EMEG |
| Gamma-chlordane |
ND - 4 |
60/310 |
7/05 |
0.5/306 |
CREG/EMEG |
| Heptachlor |
ND - 1.1 |
3/159 |
1/05 |
0.2/306 |
CREG/RMEG |
| Heptachlor epoxide |
ND - 0.3 |
4/161 |
2/05 |
0.08/0.76 |
CREG/EMEG |
| Indeno(1,2,3-c,d)pyrene |
ND - 310 |
132/302 |
48 |
0.9 |
EPA SSL |
| Iron |
1,360 - 242,000 |
108/108 |
18 |
23,000 |
HEAST |
| Lead |
ND - 17,500 |
371/372 |
42 |
400 |
EPA SSL |
| PCB-1254 (Arochlor 1254) |
ND - 10 |
2/114 |
1 |
1 |
RMEG |
| PCB-1260 (Arochlor 1260) |
ND - 18 |
11/166 |
7 |
0.4 |
CREG |
| Thallium |
ND - 42 |
3/222 |
1 |
5.5 |
HEAST |
| Zinc |
9 - 28,200 |
378/378 |
3 |
20,000 |
EMEG |
Table E4 - Contaminants in Sediment Samples above a Comparison Value
| Contaminant |
Range in mg/kg1 |
Samples > DL2 |
Samples >CV3 |
CV in mg/kg |
CV Source4 |
| Arsenic |
ND - 14 |
25/37 |
25/05 |
0.5/206 |
CREG/EMEG |
| Antimony |
ND - 56.7 |
4/37 |
1 |
20 |
RMEG |
| Benzo(a)anthracene |
ND - 2.1 |
22/37 |
5 |
0.9 |
EPA SSL |
| Benzo(b)fluoranthene |
ND - 2.3 |
24/37 |
5 |
0.9 |
EPA SSL |
| Benzo(k)fluoranthene |
ND - 25 |
21/37 |
1 |
9 |
EPA SSL |
| Benzo(a)pyrene |
ND - 2 |
24/37 |
18 |
0.1 |
CREG |
| Beryllium |
ND - 0.6 |
31/39 |
19/05 |
0.2/3006 |
CREG/RMEG |
| Cadmium |
ND - 168 |
14/37 |
1 |
10 |
EMEG |
| Chromium |
9 - 3,400 |
37/37 |
1 |
300 |
RMEG |
| DDT |
ND - 2.9 |
16/37 |
1/05 |
2/306 |
CREG/RMEG |
| Dibenz(a,h)anthracene |
ND - 0.3 |
4/37 |
2 |
0.09 |
EPA SSL |
| Gamma-chlordane |
ND - 0.7 |
7/18 |
1/05 |
0.5/306 |
CREG/EMEG |
| Iron |
ND - 49,300 |
19/29 |
1 |
23,000 |
HEAST |
| Lead |
ND - 7,640 |
31/37 |
2 |
400 |
EPA SSL |
| Total polynuclear aromatic hydrocarbons |
ND - 16.5 |
7/11 |
4 |
0.1 |
CREG* |
* This is the CREG for benzo(a)pyrene.
There is a legend for this table after Table
E7. |
Table E5 - Contaminants in Surface Water above a Comparison Value
| Contaminant |
Range in Water in mg/L7 |
Samples > DL2 |
Samples > CV3 |
CV in mg/L* |
CV Source4 |
| Arsenic |
ND - 0.08 |
24/43 |
24/05 |
0.002/0.36 |
CREG/EMEG |
| Dieldrin |
ND - 0.0004 |
18/51 |
2/05 |
0.0002/0.056 |
CREG/EMEG |
* These comparison values are multiplied by
100 because it is assumed that daily ingestion of surface water for a small
child is 10 milliliters (ml) rather than the 1 liter (1,000 ml) used for
drinking tap water.
The legend for this table follows Table E7. |
Table E6 - Contaminants in Background Sediment above a Comparison Value
| Contaminant |
Range in Sediment
(mg/kg)1 |
Samples >
DL2 |
Samples >
CV3 |
CV in mg/kg |
CV
Source4 |
| Arsenic |
ND - 11.1 |
18/22 |
18/05 |
0.5/206 |
CREG/EMEG |
| Beryllium |
ND - 0.8 |
6/22 |
6/05 |
0.2/3006 |
CREG/RMEG |
| Benzo(a)pyrene |
ND - 2.5 |
7/22 |
3 |
0.1 |
CREG |
| Benzo(b)fluoranthene |
ND - 2.6 |
7/22 |
2 |
0.9 |
EPA SSL |
| Benzo(a)anthracene |
ND - 2.9 |
6/22 |
2 |
0.9 |
EPA SSL |
| Dibenz(a,h)anthracene |
ND - 0.7 |
2/22 |
2 |
0.09 |
EPA SSL |
| Iron |
3,330 - 30,700 |
22/22 |
1 |
23,000 |
HEAST |
| Indeno(1,2,3-c,d)pyrene |
ND - 1.7 |
7/22 |
1 |
0.9 |
EPA SSL |
| Alpha-chlordane |
ND - 2.4 |
5/22 |
1/05 |
0.5/36 |
CREG/RMEG |
| Gamma-chlordane |
ND - 2 |
5/22 |
1/05 |
0.5/306 |
CREG/EMEG |
| Cadmium |
ND - 38 |
4/22 |
1 |
10 |
EMEG |
| Heptachlor Epoxide |
0.2 |
1/22 |
1/05 |
0.08/0.76 |
CREG/EMEG |
| The legend for this
table can be found after Table E7. |
Table E7 - Contaminants in Background Surface Water above a Comparison Value
| Contaminant |
Range in Surface
Water (mg/L)7 |
Samples >
DL2 |
Samples >
CV3 |
CV in mg/L* |
CV Source4 |
| Arsenic |
ND - 0.01 |
13/22 |
13/05 |
0.002/0.36 |
CREG/EMEG |
* Comparison values for drinking water were
multiplied by 100 because it was assumed that daily ingestion of surface
water for a child was 10 ml rather than the 1,000 ml used for drinking tap
water.
The legend for this table can be found after
this table. |
Footnotes for Tables E1 - E7
1 - mg/kg = milligrams of chemical per kilogram
of soil. mg/kg = parts per million (ppm)
2 - DL = detection limit
3 - CV = comparison value. See Appendix C for an explanation
of comparison values.
4 - These comparison values are described in Appendix
C starting on page 64.
5 - The samples above a CREG are the first number and
those above an EMEG or RMEG is the second.
6 - The first number is a CREG and the second is an EMEG
or RMEG.
7 - mg/l = milligrams of chemical per liter of water.
APPENDIX F - TOXICOLOGICAL EVALUATION
This appendix is a detailed chemical-by-chemical evaluation of the possible health
consequences of exposure to DDMT contaminants. These evaluations are summarized on
pages 16 and 18.
Possible Health Consequences of Chemicals found on Dunn Field
When a sample concentration exceeded a CV, the maximum level of that chemical was used to
calculate an exposure dose, which was then compared with an appropriate health guideline.
Soil Contaminants
Of the 9 chemicals in soil with concentrations above CVs, three - arsenic, alpha-chlordane, and
dieldrin, had health guidelines for non-carcinogenic health effects. There were health
guidelines to identify cancer risk for arsenic, alpha-chlordane, benzo(a)pyrene, and dieldrin
(58,77,97,98). Table D1 on page 67 contains the results for these four chemicals. Only adult
exposure doses were calculated because access of small children to Dunn Field contaminants
appears very unlikely because Dunn Field is and has always been fenced. A qualitative
evaluation of the possibility of health consequences was done for the 5 chemicals
(benzo(a)anthracene, benzo(b)fluoranthene, benzo(k)fluoranthene, dibenz(a,h)anthracene, and
indeno(1,2,3-c,d)pyrene) for which there were no health guidelines. As indicated above, the
conclusions on these 6 chemicals are applicable only to the locations sampled and not to all of
Dunn Field because of inadequate number and extent of sampling.
Arsenic
As indicated on Table D1, health effects due to arsenic in 5 Dunn Field soil samples are not
likely to occur because the concentrations are too low even when workers were assumed to be
exposed 5 days a week for 30 years.
Alpha-Chlordane
As indicated on Table D1, health effects due to alpha-chlordane in 5 Dunn Field soil samples
are not likely to occur because known concentrations are too low even when workers were
assumed to be exposed 5 days a week for 30 years.
Dieldrin
As indicated on Table D1, health effects due to dieldrin in 5 Dunn Field soil samples are not
likely to occur because known concentrations are too low even when workers were assumed to
be exposed 5 days a week for 30 years.
PAHs
Six of the substances in Dunn Field soil found above comparison values are members of the
chemical group, polycyclic aromatic hydrocarbons [PAHs] (58). These six are
benzo(a)anthracene, benzo(a)pyrene, benzo(b)fluoranthene, benzo(k)fluoranthene,
dibenz(a,h)anthracene, and indeno(1,2,3-c,d)pyrene. EPA's guidance for the quantitative risk
assessment of PAHs was used to identify maximum cancer risk for the 6 PAHs (99). This was
done because the other 5 PAHs do not have health guidelines. The additional maximum excess
cancer risk for each of the six PAHs is moderate (about 1-2 in 10,000) if someone was exposed
5 days a week for 30 years. The cumulative maximum excess risk for same length of exposure
to all six PAHs is elevated (1 in 1,000).
However, although cancer risk is elevated, the actual chance of anyone being harmed is very
low or non-existent because regular long-term exposure of any individual was unlikely. This
conclusion is based on that fact that all PAH concentrations above background from Dunn
Field came from one location. The PAH levels at the other 3 locations were 0.2 PPM or lower
and are within the PAH levels of 0.2 - 61 ppm typically found in urban soil (58). The one
sampling location with elevated concentrations was an area where petroleum products, food, or
other materials were burned (3). PAHs are produced when such materials are burned (58).
This area contaminated with PAHs would be a problem only if someone regularly worked at that spot. This appears unlikely (3,5).
Sediment Contaminants
Health effects due to the contaminants in Dunn Field sediment are very unlikely, even if
exposure was daily. Daily exposure to contaminated sediment appears unlikely. As indicated
on Table E2, the average levels of beryllium and PAHs at all 12 locations are similar to the
means identified in the background sampling of the DDMT area. In addition, the PAH
concentrations are within the levels of 0.2 - 61 ppm typically found in urban soil (58).
The 6 chemicals in Dunn Field sediment above comparison values were beryllium,
benzo(a)anthracene, benzo(b)fluoranthene, benzo(a)pyrene, dibenz(a,h)anthracene, and
indeno(1,2,3-c,d)pyrene. Of these 6, only beryllium had a health guideline for non-carcinogenic health effects. The highest concentration of beryllium was 250 lower than its
health guideline (100). Health guidelines exist to identify cancer risk for benzo(a)pyrene and
beryllium (58,100).
EPA's guidance for the quantitative risk assessment of PAHs was used to identify maximum
cancer risk for the 5 PAHs (99). This was done because the other 4 PAHs do not have health
guidelines. The additional maximum excess cancer risk for beryllium and each of the 5 PAHs
is very low (about 5 in 100,000 to 6 in 1,000,000) if someone were exposed 5 days a week for
30 years.
Possible Health Consequences of Chemicals found on DDMT Main Facility
When a sample concentration exceeded a CV, the maximum level of that chemical was used to
calculate an exposure dose, which was then compared was an appropriate health guideline.
Soil Contaminants
Of the top 10 chemicals in soil with concentrations above CVs, four (arsenic, beryllium,
dieldrin, and DDT) had health guidelines for non-carcinogenic health effects. Health
guidelines exist to identify cancer risk for arsenic, benzo(a)pyrene, beryllium, dieldrin, and
DDT (58,77,100,101). Table E2 on page 68 contains the results for these 5 chemicals for
adult exposure doses. Exposure doses for small children were also calculated because they
could have been exposed if they lived in the base housing which is located near the southeast
corner of the Main Facility. Access of small children living around the DDMT Main Facility
to on-site contaminants appears very unlikely because the main facility is and, reportedly, has
always been fenced. A qualitative evaluation of the possibility of health consequences was
done for the 5 chemicals [benzo(a)anthracene, benzo(b)fluoranthene, dibenz(a,h)anthracene,
indeno(1,2,3-c,d)pyrene, and lead] for which no health guidelines exists.
Arsenic
Health effects due to arsenic in on-site soil samples are not likely to occur. The adult exposure
doses for the maximum (84 ppm) and mean (15.7 ppm) arsenic concentrations are below the
health guideline for non-carcinogenic health effects. The child exposure dose for the maximum
arsenic level was above the arsenic health guideline, and for the mean level was below. In
Figure G1, the 30 locations are identified where arsenic concentrations are above 20 ppm.
Concentrations above 20 ppm result in a child exposure dose that exceeds the health guideline
if exposure were all day every day. However, none of these locations appear close enough to
base housing for small children to be regularly exposed. The cancer risk for the maximum
arsenic level is low and not elevated for the mean level.
Beryllium
Health effects due to beryllium in on-site soil samples are not likely to occur. The adult and
child exposure doses for the maximum and mean beryllium concentrations are below the health
guideline for non-carcinogenic health effects. The cancer risk for the maximum and mean
levels of beryllium was not elevated.
Dieldrin
Health effects due to dieldrin in on-site soil samples are not likely to occur. The adult
exposure doses for the maximum and mean dieldrin concentrations are below the health
guideline for non-carcinogenic health effects. The child exposure dose for the maximum
dieldrin level was above its health guideline, and for the mean level, it was below. In Figure
G2, the 9 locations are identified where the dieldrin concentration is above 3 ppm. Above 3
ppm results in exceeding the child comparison value if exposure is all day every day. Only
one location appears close enough to base housing for daily exposure to be likely. However,
the dieldrin level at that spot (5.5 ppm) does not represent a public health hazard. The
exposure dose for this level (0.0001 mg/kg/day) is 45 times lower than the no observed
adverse health effects level [NOAEL] and 450 times lower than the lowest observed adverse
health effects level [LOAEL] seen in the lowest valid animal study (98). No valid human
investigation has been done. The cancer risk for the maximum and mean levels is not elevated.
DDT
Health effects due to DDT in on-site soil samples are not likely to occur. The adult exposure
doses for the maximum and mean DDT concentrations are below the health guideline for non-carcinogenic health effects. The child exposure dose for the maximum DDT level of 59 ppm
was above its health guideline, but not any other concentration. However, this DDT level does
not represent a public health hazard. The exposure dose for this level (0.001 mg/kg/day) is 50
times lower than the NOAEL and 250 times lower than the LOAEL seen in the lowest valid
animal study (101). No valid human investigation has been done. The cancer risk for the
maximum and mean levels is not elevated.
Lead
A review of the ATSDR Toxicological Profile for Lead indicates that daily exposure to lead at
the locations identified on Figure G3 where lead levels were above 400 ppm, could be a health
hazard for children less than 6 years old (79). However, small children probably could not
have had enough exposure to result in health effects because none of the locations with lead
levels greater than 400 ppm are near the base housing units. Base housing appears to be the
only location where small children could regularly contact soil on DDMT. All but 2 of the
locations with lead concentrations above 400 ppm are located on the west or north side of
DDMT. The 2 locations on the same side of the facility (east) as base housing are about 600
feet away. A child under 6 could not likely travel to these two locations frequently enough to
result in harm.
PAHs
Five of the top 10 substances found above comparison values are members of the chemical
group, polycyclic aromatic hydrocarbons [PAHs] (58). These 5 are benzo(a)anthracene,
benzo(a)pyrene, benzo(b)fluoranthene, dibenz(a,h)anthracene, and indeno(1,2,3-c,d)pyrene.
EPA's guidance for the quantitative risk assessment of PAHs was used to identify maximum
cancer risk for the 5 PAHs (99). This was done because the other 4 PAHs do not have
health guidelines. The additional maximum excess cancer risk for each of the 5 PAHs was
low (1 in 10,000) to elevated (5 in 1,000) for the maximum levels but was not elevated for
the mean levels if someone were exposed 7 days a week for 70 years. The cumulative
additional excess risk for exposure to the maximum concentrations of all 5 PAHs is elevated
(7 in 1,000).
However, this elevated cancer risk is focused around the west side of Building 629, the south
side of Building 249 and between Buildings 689 and 690. Any individual who had or has
regular contact with soil from these three locations for many years would have an elevated
risk of cancer from exposure to PAHs. Whether anyone would have experienced this
exposure situation is unclear. Risk of cancer does not appear to be elevated for the rest of
the DDMT Main Facility because PAH concentrations are considerably lower.
These conclusions are based on the fact that the highest concentrations for each of the 5
PAHs came from the three sampling locations identified in the previous paragraph. The
PAH levels found at most of the rest of the Main Facility sampling locations are within the
PAH levels of 0.2 - 61 ppm typically found in urban soil (58).
Sediment
The 15 chemicals in on-site sediment samples with concentrations above a CV (Table E4), do
not currently present a public health hazard. These 15 are arsenic, antimony,
benzo(a)pyrene, benzo(a)anthracene, benzo(b)fluoranthene, benzo(k)fluoranthene,
beryllium, cadmium, chromium, dibenz(a,h)anthracene, DDT, gamma-chlordane, iron, lead,
and total polynuclear aromatic hydrocarbons (PAHs). All the samples with concentrations
above CVs, except for gamma-chlordane, were taken from Lake Danielson or the golf course
pond. Figures G5 and G6 (pages 86 and 87) display the contaminant levels for arsenic and
dieldrin. The sampling locations for the other 13 contaminants are the same as for these 2
chemicals.
It is not plausible that anyone could have been exposed on a regular basis to the sediments in
the lake or pond as they would have to ingest the sediment. Indirect exposure to sediment
contaminants through ingestion of fish from Lake Danielson or the golf course pond may
have occurred before 1986 when fishing was banned because elevated levels of DDT,
dieldrin, chlordane, and chlorpyrifos were found in sediment and fish tissue samples (3).
The single sample of gamma-chlordane above the CV was found in the drainage for the
western side of the main facility. For anyone to have regular exposure to sediment from any
of these locations does not appear to be plausible because there appears to have been no
facility operations at these locations (47).
Surface Water
The chemicals in the on-site surface water samples with concentrations above CVs (Table
E5), do not present public health hazards because the risk of cancer and other effects is not
significant. Two chemicals, arsenic and dieldrin, were above CVs (Figures G7 & G8). The
maximum levels of arsenic and dieldrin are well below the noncarcinogenic health effects
comparison values and the additional lifetime cancer risk from exposure to them is not significant (2 in 1,000,000 to 4 in 100,000).
APPENDIX G - CONTAMINANT MAPS
Note: The 8 maps in this appendix display the sampling locations and concentrations for the
top contaminants at DDMT. These were arsenic, benzo(a)pyrene, dieldrin, and lead
in soil; arsenic and benzo(a)pyrene in sediment; and arsenic and dieldrin in surface
water. The concentration ranges displayed on these maps are based on the
comparison values for each contaminant. The contaminant data displayed on these
maps came from electronic files provided by DDMT through the Corps of Engineers
and their contractor, CH2MHILL. The latitudes and longitudes for nearly all the
sampling locations were also provided electronically to ATSDR by CH2MHILL. Some
sampling locations for the 1990 RI were estimated by ATSDR using Figure 2-1 in the
1990 RI (3). The streets, creeks, and railroads displayed on the maps in this
appendix come from the TIGER files generated by the U.S. Census Bureau. The
locations of the open drainage ditches and the DDMT site boundaries were estimated
by ATSDR using Figure 3-1 from 1990 RI and Drawings 1 & 2 from the 1995 Generic
RI/FS Workplan (3,67).
Figure G1 - Arsenic in Soil
Figure G2 - Dieldrin in Soil
Figure G3 - Lead in Soil
Figure G4 - Benzo(a)pyrene in Soil
Figure G5 - Arsenic in Sediment
Figure G6 - Benzo(a)pyrene in Sediment
Figure G7 - Arsenic in Surface Water
Figure G8 - Dieldrin in Surface Water
APPENDIX H - ANALYSIS OF SURFACE WATER PATHWAY
Evaluation of Surface Water Drainage around DDMT24
(1) Water on the southeast side of the main facility flows through concrete-lined ditches to
four discharge points near the southeast corner [47]. The water then flows into 4 shallow
unlined ditches off-site. These ditches eventually combine and discharge into Nonconnah
Creek to the west of the airport. One of these 4 ditches flows through a neighborhood
(Muller Road) between Ball and Ketchum Roads [49]. ATSDR staff have observed children
playing in this ditch [48].
(2) On the westside of the main facility, water flows through pipes and ditches to a discharge
point midway between the north and south ends of the main facility [47]. This water flows
west through the neighborhood west of DDMT in the Tarrent Branch, which is now a lined
ditch but earlier was a natural intermittent stream. This branch eventually runs into
Nonconnah Creek near the junction of I-240 and I-55.
As displayed on Figure 5, drainage plans for DDMT from 1953 and 1960 identify a second
open ditch coming off the west side of DDMT between Tarrent Branch and Dunn Avenue
(63,62). This ditch was not displayed on a 1982 map, so it appears that sometime between
1960 and 1982, the on-site drainage was altered so that the water that once left the site in this
ditch, was rerouted to Tarrent Branch (7).
(3) Drainage from all of Dunn Field, except the northeast corner, flows to the west side of
Dunn Field and exits at three points [47]. Water at the northern most of these points flows in
a shallow unlined ditch through that portion of Rozelle Street to the west of Dunn Field.
This ditch then discharges into a lined ditch that runs east and west at the south end of this
isolated segment of Rozelle Street. This lined ditch also receives the water from several
industrial discharge points before it runs by the end of Rozelle Street.
After leaving the Rozelle area, this ditch goes into a pipe, then goes under the Illinois Central
railroad line, and then goes northwest [49]. This pipe discharges into Cane Creek between
Hamilton High and the Elvis Presley Blvd. Bridge, just downstream from the high school.
Therefore, water from the Dunn Field/Rozelle area apparently does not currently flow under
Hamilton High. However, long-term residents indicate that an open ditch used to carry
water from Dunn Field to Cane Creek so people living in this area could have had contact
with water from Dunn Field.
(4) Water from the northeast corner of Dunn Field drains into 2 lined ditches that cross
Dunn Field [47]. These ditches drain at least some of the neighborhood south of Person and
Hayes. These 2 ditches join before leaving Dunn Field. Another discharge point drains the
north end of Dunn Field (Figure 5). These 3 ditches run into Cane Creek north of the Ragan
Street Bridge and upstream of Hamilton High School. Thus, water from the northeast corner
of Dunn Field does flow under Hamilton High School.
(5) Water from the northern side of the main facility moves off-site in a lined ditch at Dunn
and Custer Streets or in storm sewers [3,47]. The ditch at Dunn and Custer switches from a
lined ditch to a pipe and back to a lined ditch before flowing into a large-lined ditch that runs
southeast to northwest to the northeast of the main facility [47]. This large ditch flows into
Cane Creek to the north of the Ragan Street Bridge [3]. The storm sewers appear to flow
directly into Nonconnah Creek [3]. Thus, some of the water from the northern side of the
DDMT Main Facility does flow under Hamilton High School, but the rest goes directly to
Nonconnah Creek.
(6) Water from the central east portion of the Main Facility, which is the area around the
DDMT Administration Building, leaves the site in storm sewers which appear to discharge
into Nonconnah Creek [3,5]. Thus, water from around the administration building does not flow under Hamilton High School.
1. The information in this section is based on comparison of the data displayed on Figure 4 to 1990 U.S.
Shelby County census data.
2. Based on several discussions with DDMT staff.
3. Sampling of the area around DDMT was done in late 1995. Sampling locations were selected by staff
from DDMT and its contractors, EPA, TDEC, and ATSDR; and a local environmental activist. This last
individual was at the time a co-chair of the DDMT RAB.
4. From discussion with Denise Cooper, DDMT, on January 27, 1997.
5. A former worker indicated to John Crellin on September 9, 1999, that some workers performed
cleanup and other tasks on Dunn Field periodically. They would work on Dunn Field 8 hours a day for several
days in a row.
6. Conversation with DDMT-CCC member in November 1998.
7. Conversation with a member of DDMT-CCC during a site visit in June 1997.
8. These population estimates were made by John Crellin using geographic information systems (GIS)
techniques. After creating 100- and 500-foot zones around the five drainage ditches, population numbers for
these 2 zones were then identified using 1990 census data for Shelby County.
9. The Memphis Fire Department estimated immediately after the incident that 1,500 - 2,000 gallons
were released (64). After the incident, the Depot estimated that only 327 gallons had been released and that this
was diluted by 37,000 gallons of rainwater (65).
10. These data were provided to ATSDR in September 1998 as an electronic file. The actual sampling of
these locations was done in late 1995. Sampling locations were selected by staff from DDMT and its
contractors, EPA, the Tennessee Department of Environmental Conservation, and ATSDR; and a local
environmental activist. This last individual was at the time a co-chair of the DDMT RAB.
11. Discussion with Michael Grayson, Health Physicist, Federal Facilities Branch/DHAC/ATSDR.
12. Discussion with Denise Cooper, DDMT environmental staff, on January 27, 1998.
13. Conversation among a DDMT-CCC member, John Crellin, Rueben Warren, Sandee Coulberson, and
others on September 9, 1999.
14. This is based on an evaluation of the ground elevations found on the USGS topographic map for the
DDMT area and my (John Crellin) observations of the area.
15. The concerns about breast cancer, prostate cancer, and hypertension were identified during a public
availability session on May 29, 1998.
16. Phone call to John Crellin from a DDMT-CCC member on March 24, 1998.
17. John Crellin had several conversations concerning this issue: conversations with a DDMT-CCC
member in March and April 1998, with Ben Moore (ATSDR) in March 1998, with Glen Kaden (DDMT) in
March 1998, and with Shawn Phillips (DDMT) in August 1999.
18. This is based on a discussion with a DDMT-CCC member on January 21, 1999. This individual
drove me (John Crellin) by Norris and Dunn Elementary. I agreed that these two schools are about the same
distances from the western boundary of DDMT.
19. This concern was expressed to John Crellin on October 17, 1998 by a DDMT-CCC member.
20. This response was developed with the guidance of Allan Susten, Ph.D., DABT. He is the Assistant
Director of Science in ATSDR's Division of Health Assessment and Consultation.
21. These toxicologic thresholds would be the no or lowest observed adverse effects levels (NOAELs and
LOAELs) for the chemical of interest.
22. This has been expressed by former workers on several occasions including the January, March, and
April 1999 Restoration Advisory Board (RAB) meetings.
23. This is a list of the substances tested for in any of the 4 recent environmental sampling programs at
DDMT. The actual number of parameters tested in any one of the 4 programs varied from about 70 in the 1995
RI program to about 200 in the screening sites program.
24. See Figure 5 on page 24 for a visual description
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