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                  <text>&lt;p style="margin-top: -1em; line-height: 1.2em;"&gt;The Alvin L. Young Collection on Agent Orange comprises 120 linear feet and spans the late 1800s to 2005; however, the bulk of the coverage is from the 1960s to the 1980s and there are many undated items. The collection was donated to Special Collections of the National Agricultural Library in 1985 by Dr. Alvin L. Young (1942- ). Dr. Young developed the collection as he conducted extensive research on the military defoliant Agent Orange. The collection is in good condition and includes letters, memoranda, books, reports, press releases, journal and newspaper clippings, field logs and notebooks, newsletters, maps, booklets and pamphlets, photographs, memorabilia, and audiotapes of an interview with Dr. Young.&lt;/p&gt;&#13;
&lt;p&gt;For more about this collection, &lt;a href="/exhibits/speccoll/exhibits/show/alvin-l--young-collection-on-a"&gt;view the Agent Orange Exhibit.&lt;/a&gt;&lt;/p&gt;</text>
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&lt;p&gt;For more about this collection, &lt;a href="/exhibits/speccoll/exhibits/show/alvin-l--young-collection-on-a"&gt;view the Agent Orange Exhibit.&lt;/a&gt;&lt;/p&gt;</text>
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&lt;p&gt;For more about this collection, &lt;a href="/exhibits/speccoll/exhibits/show/alvin-l--young-collection-on-a"&gt;view the Agent Orange Exhibit.&lt;/a&gt;&lt;/p&gt;</text>
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&lt;p&gt;For more about this collection, &lt;a href="/exhibits/speccoll/exhibits/show/alvin-l--young-collection-on-a"&gt;view the Agent Orange Exhibit.&lt;/a&gt;&lt;/p&gt;</text>
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°1353

Author

Barnes, Donald G.

Corporate Author
Report/Article TltlO Memorandum: FDA Risk Assessment for Higher
Chlorinated Dibenzo-p-dioxins, from Donald G. Barnes
to Alvin Young and others, May 13, 1983

Journal/Book Title
Year

0000

Month/Day
Color

D

Number of limps 21
DeSCTlptOn Notes

Includes as an attachment this article: "The Use of
Epidemiology in the Regulation of Dioxins in Food
Supply," Regulatory Toxicology and Pharmacology, 1,
379-387(1981).

Thursday, May 03, 2001

Page 1353 of 1403

�UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
tp

WASHINGTON, D.C. 20460

&lt;

1 3 1983
OFFICE OF
PESTICIDES AND TOXIC SUBSTANCES

MEMORANDUM

TO:

Addressees

SUBJECT:

FDA Risk Assessment for Higher Chlorinated
Dibenzo-p-dioxins

Attached is a recently prepared risk assessment by the
Food and Drug Administration for hexa-, hepta- and octachlorodibenzo-p-dioxins in chicken eggs.
I believe the analysis presented here is an interesting
one and could provide fodder for a future first Friday feed.

Donald G. Barnes, Ph.D.
Senior Science Advisor to the
Assistant Administrator
for Pesticidees
and Toxi-'C, .Sujsst-.ances
Attachment
Addressees :
Lisa Barrera
Pat Roberts
Judy Bellin
David Vanormer
Priscilla Holtzclaw
Bob McGaughy
(/Al Young
Carl Keller

A-101
'-'
A-132
WH-565
TS-769C
WH-548D
RD-689
f
Veterans Adm. &lt;£— T4
NIEHS

�DEPARTMENT OF HEALTH &amp; HUMAN SERVICES

Public Health Service

Memorandum
Date

April 29, 1983

Prom

Acting Chief, Contaminants &amp; Natural Toxicants Evaluation Branch (HFF-159)

Subject

Levels of Concern for Hexa- (HCDD), Hepta- (HpCDD) and
Octachlorodibenzo-p-dioxins (XDD) in Chicken and Eggs

To

Mr. John Taylor
Director, Division of
Guidance (HFF-310)
Through: Dr. Gary Flamm
Acting, Associate Director for Toxicological Sciences (HFF-100)
As a result of concerns for higher chlorinated dioxin contamination of
chickens and eggs the Texas Department of Health has requested "that FDA
provide guidance as to health or regulatory significance as well as action
guidance" (W. Remle Grove, see attachment # 1). In response to this
request, as submitted through DRG, we have reviewed the available
information on the toxicity of several dioxin congeners. Based on this
review we are suggesting the following levels of concern (LOG) for these
substances in chicken and eggs.
Levels of Concern^/
HCDD
HpCDD
OCDD

300 parts per trillion
500 parts per trillion
3 parts per million

a/ Because the amounts of chicken and eggs consumed are similar, a
uniform level of concern for the respective contaminants can be applied to
each food item.
The rationale, biological and/or toxicological end-points and factors
utilized in the development of the above LX are identified in subsequent
pages and attachments. It is important to recognize that the available
literature from which these levels were derived is limited.
We emphasize that these levels apply only to the present situation in Texas
.and do not have general applicability to contamination by the dioxin
congeners HCDD, HpCDD and OCDD in food. In this situation the various
isomers of each congener will not be dealt with individually but rather as
a group (e.g., as congeners). This is so because of a lack of- a)
biological and/or toxicological studies on specific isomers, and b)
knowledge of the presence of individual isomers involved in the Texas
situation. It should also be noted that while the carcinogenicity of these
congeners was assssed, where specific studies were available, the potential
exposure to them in the Texas incident is considered to be of a relatively

�-2-

short duration (e.g.,-possibly several weeks up to several months).
Therefore, carcinogenic potential was not used as the toxicological
determinant in deriving the LXs for dioxins in chicken and eggs. It is
equally important to recognize that other toxic manifestations, such as
reproductive and/or teratogenic effects, may result from pulse (single) or
short-term (days to weeks) exposures to dioxins such as the HCDD congener.
It is the concern for these non-carcinogenic effects which serves as the
basis for our evaluation, again since lifetime exposure is not an issue.
Since the tetrachlorodibenzo-p-dioxin (TCDD) congener is the best studied
and most toxic member of this class of toxicants, the health assessment
performed on tha presence of TCDD in freshwater fish from various areas of
the Great Lakes (F. Cordle, Reg. Tox. Pharm., 1;379-387, 1981; see
attachment # 2) will be used as the basis for the establishment of LXs for
HCDD, HpCDD and OCDD. In that assessment it was determined from a
multi-generation reproduction study in rats that the no-effect level for
TCDD was 1 nanogram (ng)/kg b.w./day. In keeping with these findings, a
concern level of 25 ppt TCDD in fish was recommended by FDA to State
officials. The value of 25 ppt TCDD and a fish consumption value of 37
g/day (99th percentile) is used in the present assessment to derive maximum
daily intakes for the other dioxins (HCDD, HpCDD and OCDD) based on
appropriate safety factors and their biological and/or' toxicological
potency in relation to TCDD.
In order to evaluate the relative biological/toxicological potency of these
toxicants, several different types of studies were assessed. A number of
studies have shown that there is a distinct relationship between the
ability of the dioxins to elicit several of their toxic and/or biological
manifestations and to bind to a cytosolic-receptor. These studies have
shown that for the dioxins to produce any appreciable degree of
toxicological and/or biological activity the four lateral ring positions
must be occupied by chlorine atoms and at least one ring position must be
unsubstituted.
The comparative induction of aryl hydrocarbon hydroxylase (AHH) by a number
of dioxins, including TCDD, HCDD, HpCDD and XDD has been studied in rat
hepatoma cell cultures by J. Bradlaw and co-workers (Fd. Cosmet. Tox.,
.18:627-635, 1980). Their studies showed that the relative potency of the
most active congeners of HCDD, HpCDD and XDD were 1/10, 1/200 and 1/25,000
of that of TCDD (relative potency of 1), respectively. In similar studies
performed ty A. Poland and associates (Mole. Pharm., 2-736-747, 1973) on
AHH induction in chicken embryonic livers, the relative biological potency
Of HCDD was determined to be approximately 1/4.5 when the potency of TCDD
was 1, while OCDD was shown to be inactive.
Another type of study which was used to evaluate relative toxicological
potency was acute oral toxicity. The following table is a compilation of
acute oral LD5QS in the guinea-pig for those congeners that have been
studied (from 3. Huff and co-workers, Enviro. Heal. Perspec.. 36:221-240,
1980).

�-3-

Single Oral LD$Q
(ug/kg b.w.)
Congener
2,3,7,8-TCDO
1,2,3,4,7,8-HCDD
1,2,3,6,7,8-HCDD
1,2,3,7,8,9-HCDD
1,2,3,4,6,7,8-HpCDD

Guinea-pig
2
73
70-100
60-100
&gt; 600

Acute oral toxicity of dioxin congeners has been studied in other species,
however, the guinea-pig is being used in this analysis because on an acute
basis it is the most sensitive species. An examination of these values
reveals that the acute oral LDjns for the three HCDD isomers are very
similar. To compare the acute toxicity of HCDD to that of TCDD the lowest
reported value of 60 ug/kg b.w. will be used. As in the previous
derivation of relative potency, if TCDD is given a value of 1, it follows
that the relative potency of HCDD is 1/30 (60 ug/kg-HCDD/2 ug/kg-TCDD) of
that of TCDD. Relative potencies for HpCDD and OCDD could not be
calculated, because the acute LD$Q for HpCDD was not specifically
identified ( &gt; 600 ug/kg b.w.) and no value for OCDD has been reported.
A number of reproductive/teratogenic studies have been performed with TCDD,
HCDD and OCDD, while none have been reported for HpCDD. In these studies
the lowest no observed effect level (NOEL) for TCDD was shown to be at a
dosage of 0.001 ug TCDD/kg b.w./day (3-year rat reproduction study; F.
Murray and co-workers, Tox. Appl. Pharm., 50:241-252, 1979). In a
teratology study by B. Schwetz et al. (Enviro. Health Perspec.. 5_: 87-99,
1973) the lowest dosage shown not to effect embryonal or fetal development
for HCDD was 0.1 ug/kg b.w./day. In this same study OCDD did produce
embryotoxicity (subcutaneous edema), but no teratogenic effects at 500
mg/kg b.w./day, however, the next lowest dosage, 100 mg/kg b.w./day, did
not cause either teratogenic or embryotoxic effects. In comparing the
NOELs for these dioxins a relative potency of 1 is assigned to TCDD. It
follows that the relative potency of HCDD is 1/100 and that of OCDD is 1/1
X 108 in terms of reproductive toxicity/teratogenicity.
Only one of the congeners of interest, namely HCDD, has been studied in a
long-term carcinogenic bioassay (NCI, Technical Report Series No. 198, NTP
No. 80-12, 1980). In this study a mixture of two isomers, 1,2,3,6,7,8- and
1,2,3,7,8,9-HCDD, was shown to exhibit a lowest effect level (uEL) for
neoplasia in B6C3F1 mice of 0.2 ug/kg b.w./day. This compares to the LEL
of 0.01 ug/kg b.w./day which was observed by Kociba and co-workers (Tox.
Appl. PhaTm., _46:279-303, 1978), in a two-year chronic study in rats. The
relative ootency for neoplasia of HCDD in comparison to TCDD would,

�-4-

therefore, be 1/20. It must be emphasized that in this instance the toxic
end-point of neoplasia was used solely to derive a relative potency factor
for HCDD, not to address the issue of carcinogenicity, per se.
The following table contains a summary of the relative potencies determined
for HCDD, HpCDD and OCDD by the methods discussed above.
Relative Biological/Toxicological Potencies*
Dioxin
Conqenar

AHH Induction
Chicken Liver
Rat
Embryo
Hepatomas

1

1

1/4.5

1/10

HpCDD

NR

1/200

OCDD

NA

1/25,000

Acute
Oral
LDsn

TCDD
HCDD

'

Reproductive/
Teratogenic
Carcinogenic
Bioassay
Studies

1

1

1

1/100

1/20

NR

NR

NR

NR

1/1 X 108

NR

1/30

* - 1 is the highest level of activity.
NR - not reported; studies have not been performed.
NA - not active
It is apparent that of the three congeners of interest HCDD demonstrates
the greatest activity with HpCDD and OCDD following in order of magnitude.
This follows the structure activity relationship for this class of
compounds which indicates that those congeners with chlorines in positions
2,3,7 and 8 and with at least one unoccupied ring position will demonstrate
the greatest biological/toxicological activity.
Derivation of LQCs
HCDD
The relative potencies of HCDO derived from the various studies cited above
range between 1/4.5 and 1/100. Since the incident in question involves an
acute or short-term exposure the risk of a pulse (single) exposure during
pregnancy would be of most concern. Therefore, while not ignoring the
trend suggested by the smaller relative potency factors for HCOD, more
weight is given to the larger factor determined on the basis of the
teratogenic study performed with HCDD. It was, therefore, decided that a
more appropriate relative potency for HCDD is 50. This was then used to
derive the LOG for HCDD according to the following calculation -

�25 ppt* X 50 X (36.8 g/53.9 g)** = 853 ppt (rounded to 850 ppt)
*-• The 25 ppt used in this calculation is the health advisory level which
was issued for the TCDD contamination of fish from the Great Lakes. As
it was stated previously it is the Great Lakes health advisory which is
used as the basis for the derivation of the levels of concern for the
higher chlorinated dioxins in the present assessment.
**- ratio of food factors; 36.8 g/day - 99th percentile intake for fish;
53.9 g/day - total intake for eggs (28.5 g) and chicken (25.4 g)
consumed by children 2 to 5 years of age (supplied by Dr. F. Cordle,
HFF-108, 4/14/83, see attachment #3).
This level of' 850 ppt, however, applies to the adult and not to children.
The latter are of greater concern in this case because they are likely to
consume more eggs and chicken per kg of body weight than adult. Therefore,
the 850 ppt level is divided by a factor of 3 to account for this increased
exposure of children to give a value of 283 ppt which is rounded off to
give a LOG of 300 ppt for HCDD.
HpCDD
The amount of data available on HpCDD is quite meager. If the relative
potency value of 1/200 is used, a LOG is derived which is unduly high,
particularly in light of the information on the structure-activity
relationship of the dioxins. The two hepta isomers have chlorine atoms at
carbon positions 2,3,7, and 8, one unoccupied carbon position, and only
differ from the most toxic hexa-isomers by the presence of one additional
chlorine atom. Therefore, it is felt that a LOG of 500 ppt would be more
appropriate.

XDD
After evaluating the available information on the toxicological and/or
biological potency of XDO it was determined that the most reliable data
was that from the reproductive/teratology study reported by Schwetz e_t al.
(1973). In that study the NOEL for OCDD was 100 mg/kg b.w./day Using this
value together with a 1000 fold safety factor and accounting for the lower
body weight of 2 to 5 year old child, a tentative LOG of concern equivalent
to 30 ppm was determined, as shown below:
' LOG =
a
«
a

100 mg/kg b.w./day (NOEL) $ 1000 (S.F.)
0.1 mg/kg b.w./day x 16 kg b.w. (child)
1.6 mg/day f 53.9 g/day (total consumption of
chicken and eggs by child)
29.68 ppm or 30 ppm

Wh:!le the value is based on "in vivo" experimentation, it appears to be
unrealistically high for a congener which belongs to a class of toxicants,
e.g., dioxins, for which so much concern has been expressed. Furthermore,
it should be stressed that this value is derived from a single study using

�-6-

only one animal species, e.g., the rat. If we consider the-"in vitro" data
on AHH enzyme induction, it is seen that OCDD has only a minute fraction of
the activity reported for TCDD. Nevertheless, there is some concern over
the possibility that exposure to OCDD at the level suggested by the
tentative LOG of 30 pprn may result in some degree of enzyme induction
activity in humans. Therefore, the application of a further safety factor
of at least 10 is considered appropriate. Thus, a LOG of 3 ppm is
recommended for OCDD in chicken and eggs.
Since the amounts of chicken and eggs consumed are similar, a uniform LOG
for the respective congeners can be applied to each food item. Again it
must be emphasized that these levels apply only to the present situation in
Texas and have rio application to other incidents. It should also be
reiterated that while the induction of neoplasia was used to derive one of
the comparative relative potency factors for HCDD the issue of
carcinogenicity was not utilized directly in this evaluation because of the
limited, short-term exposure of this situation. Finally, although
structure-activity information was considered in deriving the LQCs for the
higher chlorinated dioxins it is recognized that additional data on such
relationships is required to refine the significance of such parameters in
the toxicoldgical assessments of these toxicants.

ichael Bolgef, Ph.D.
Garfield N. Biddle, Ph.D.
Attachments
cc:
HFF-100

HFF-150 (Blumenthal)
HFF-152 (Jackson/Edwards)
HFF-159 (Shibko)
HFF-159:GNBiddle:MBolger:clw:4/29/83:472-5706:2095A

�15. 83--261-360

m PROCESS

12 SUBS - SCRAPINGS

FROM EQUIPMENT
lb. 33-292-061
1 SUB - SHEEP WOOL FROM SHEEP
HEAL SCREEN
RECEIVED FROM H.T.C. RENDERING,
SAN ANGELO, TEXAS
j?. 83-261-062
1 SUB - «EAJ S BONE HEAL
SHEEP HEAL
18, 83-292-063
1 SJ!J - POULTRY MEAL

!•&gt;. S3- 292- 064
1 SUB - POULTRY HEAL
20. 83-232-065
1 SUB - MEAT 1 BONE MEAL
*Ji. 33-292-066
1 SUB - POULTRY HEAL
i2. 82-292-067
1 SUB - HEA1 1 BONE HEAL
L'li. 83-292-068
J SUB - MEAT I BONE HEAL
:'. 33-2^2-069
;.
1 SUB - UlftTf DEBRI5» ffcOH
IKS7PE HEARTH OF OLD
1NCENERATOR

•:.Mirriii 10 ciNCiMMAii LABORATORY:
23 SUBS - LUBRICANTS, DEORORANTS,
INSECTICIDES. BOILER
COMPOUNDS, VARIOUS
LIQUIDS ANO POUtERS.
UPON RECEIPT OF C/R'S, I WILL DESCRIBE SUBS THAT RELATE TO EACH SAMPLE.
i.M RICAKDS TO 83-261-350, SUB 41 HEAT t bONE MEAL* SUB 42 ANIHAL FAT,
COLLECTED 5ROH LOAPS RECEIVED FROM TEXAS 6Y PRODUCTS COMPANY, SAN ANTONlD. IT
miEVElr TKAt B0TK COMPANIES #RF UNUER THE SftKE 0«NE«T, 1K1S: «2tt &amp;
4/11/83. AS TO COMMON SUPPLIERS, PROCESSING, ETC.

�&lt;'«JTL THAI 83-261-350. COLLECTED ON 4/4/83 WAS RECEIVED FROM TEXAS BY-PRODUCTS
mnt-ANY, SAN ANTONIO, TEXAS. SUB *1 HF.AT 1 BONE HEAL WAS COLLECTED FROM THE
TRANSPORT TRUCK, AND ANALYSIS REVEALED 25.!&gt; PPK. OUR SAMPLE 83-260-356. MEAT
i BONE MEAL. COLLECTED 0« 3/H/B3 REVEALED 16.0 ?pH TCP'S. THIS SAMPLE WAS
COLLECTED FROM A STORAGE BIN, AND IS NOW BELIEVED TO BE A PORTION RECEIVE*
n»DH TEXAS BIT-PRODUCTS.
TEXAS WNUER1N6 IS OWNED BY HUBEW L. L1NENBERQER, AND ALSO FUNCTIONS AS THE
PRESIDENT. LINENBER6ER ALSO OWNS 75* OF THE STOCK OF TEXAS BY-PRODUCTS, SAN
'.rtlOMlO, AS WELL AS OWNING A hAJOR INTEREST 1M TEX -HENS, INC., MIXON, TEXAS.
TE/.AS kENliERlNG RECEIVED APPROX. 3-4 LOADS OF HEAT I BONE iiEAL PEft WEEK FROM
TrxAS BY-PRODUCTS, ESTIMATED AT APPROX. 150,000 LBS. OK MORE. IT WAS REPORTED
THnT THIS HEAT 1 BONE HEAL IS VERY HIGH IN FAt CONTENT AND IS RUN THROUGH THE
EQUIPMENT AT TEXAS RENDERING TO EXTRACT ADDITIONAL FAT, IT IS ALSO REPORTED
THAT PRODUCT SAMPLED UNDER 03-261-350, SUB 12, ANIMAL FAT FROM TEXAS
ST-PRODUC7S IS ACTUALLY STREET GREASE. Ml IS NOT ANIMAL FAT PROCESSED BY
ANTONIO. REPORTEDLY DOES TO JACOB-SIERNS, HOUSTON, TEXAS.
WHILE TEXAS PJNDER2WJ RECEI'/ES KEAT I PONE HEAL AND STREET GREASE- FROK TEXAS
BY-PRODUCTS, SAN ANTONIO, TEXAS RENDERIMf, JOES NOT SHIJ1 PRODUCTS TO THEM.
ALSO IT WAS REPORTED, THESE FIRMS DO NOT HAVE COMMON SUPPLIERS. ALSO NO
PRODUCTS ARE SHIPPED PROM TEXAS RENDERING TO TEX-HENS, INC., NIXON, TEXAS.
(. GENERAL PROCESSING FLOW AT TEXAS RENDERING IS AS FOLLOWS:
AS PRODUCT IS RECEIVED, HEAT X BONE MEAL, DEAD ANIMALS, SCRAPS, ETC., IT IS
^JftPED JKTO A P3T WHERE 37 IS AUGCRED TO 70 AH 3NI&gt;US?kiAL 6K3MER, AUGERS OVER
rAGMETIC PLATE (REMOVE HE? AD TO MEAT STORAGE VAT, 10 QHE OF 5 HEAT COOKERS.
THE COOKERS ARE CHARGED WITH APPROX. 6,000 L*S. OF PRODUCT AND APPKOX. 2,000
LK-. OF ANIMAL FAT- JS ADBE&amp; (USUALLY PROCESSED THE rtiGHT BE?OR£&gt;. AFTER
COOKING AT APPROX, 313 DEGREES t. THE PRODUCT EXITS AND SCREENED WITH THE FAT
V.CIM13 TO ONE OF 3/20,000 LB. WORKING VATS. THE FAT IN THESE VAIS IS USED TO
INTO THE COOKING VATS AS STATED ABOVE.
IS NKXBCD FROM THESE WORKING VATS. IT MAINS TO A FLAT DRYING VAT TO

»&gt;r off WATER. FROM HERE, XT. is PUMPED TO EITHER OF 3/30,000 LF\ STORAGE VATS.
^r. THE MEAT EXITS THE COOKER, IT GOES TO THE PRESSES «HESE BORE FAT IS
UTKACTED (PAT GOES TO THE WORKING VATS). THE MEAT THEN PASSES THE SCfcEENEJc,
.MJBCIXI kA»a« ftiaeso A* »««4S, MAIM, »*o.t &gt;H».» M«MOV»». *M» HBis* *t*0*4 ««aa *o

T'riE HAMMER t»U. THEM THE MEAt T&amp; EITHER OF 8/60,000 t&amp;3. STORAGE BINS AS
iTMISHED MEAL. THE BONES, ETC., REMOVED BY THE SCREENER, GOES BACK TO THE
L'KJSINAL AUGER AT THE STARTING POINT OF THE PROCESS.
L'JSCUSSIONS WERE HELD OK MONDAY. 4/U/83, BY HOUSTON STATION WITH OFFICIALS Of
TrlC TEXAS KEPT. OF AGRICULTURE AND TEXAS DEPT. OF HEALTH AND OUR SAMPLE
ilTSULIS KNOWN AT THE PRESENT TIME WERE PISUCSSED. THE INTRASTATE SHELL EG^S
«t*£ DISCUSSED WITH TEXAS DEPT. OF HEALTH, HOWEVER, THEY DO MOT HAVE THE

:«*AmniES OF ANALYSING FOR POP'S 10- DETESHINEiTHS CU»*EM STAJUS- or EGGSC t
A

"P:0n SMITH FARMS AMD POSSIBLY OTHERS. !PJ^
**&lt;WHifc- CU5RENT ASSAYS. THEY
\Ki «ILL1HG TO ACT., HOWEVER ^REQUESTED THAT FDA PRO'/lIiE GUIDANCE AS TO HEALTH
'•¥" REGULATORY SICNifANCE AS WELL AS ACTION GUIDANCE.

�nr xcxft* DEFT. OF AGRICULTURE IS QUITE CONCERNED AND 15 CURRENTLY
lVG SAMPLES SUBMITTED BY 1KB F1RH OF FINISHED PROBUCT, HO«BVBR&gt; THEY
•ilSO R£QU£S7£H
TKun THE HIGH LEVELS Of ?C?'&amp; FOU*fB IW «EAI I BOME HEAL FUtOM TEXAS
Pr-PRQPUClS, SAN ANTOfilO, IT A?f-EARS THAT THIS COULD BE A CONTINUOUS SOURCE OF
LOfJTAMiNATEB PRODUCTS. AN INVESTIGATION OF THIS FIKH IS CURRENTLY BEING.
UISUUSSED.

�/'*•
REGULATORY TOXICOLOGY AND PHARMACOLOGY 1, 379-387 (1981)

The Use of Epidemiology in the Regulation of Dioxins
in the Food Supply1

FRANK CORDLE
Epidemiology and Clinical Toxicology, Bureau of Foods, food and Drug Administration,
Washington, D. C. 20204

Received November 1981

Residues of teirachlorodibenzo-p-dioxins (TCDD) were detected recently in several species
of freshwater fish from various areas of the Great Lakes. Concern for the potential human
health risk associated with the consumption of these fish prompted the Food and Drug Administration to assess epidemiological and toxicologies! TCDD data in order to determine the
need for regulatory action. In the assessment, pertinent animal and human data and daia for
the TCDD residues in the freshwater fish, for the amounts of the different fish species consumed
and for the number of individuals who consumed the fish, were evaluated. The various methods
of evaluation used to reach a regulatory decision are described.
*

INTRODUCTION
Although epidemiology may have first been used by Hippocrates, the definition
or meaning has undergone some significant changes since then. First described as
the study of epidemics and, later, as the study of the determinants of differences
in disease distributions in human populations, epidemiology today, especially in
regulatory agencies, refers essentially to the activities of the epidemiologist. In a
regulatory agency such as the Food and Drug Administration (FDA) the role of
the epidemiologist is to assimilate, digest, and synthesize the best available data
from survey, clinical, and laboratory experiences, either firsthand or from the scientific literature: these human and animal data are then combined and interpreted
in order to address a basic question: Does the evidence of adverse human health
effects from exposure to the various chemical substances that fall under FDA
regulatory authority present a risk to public health safety that is sufficient for FDA
to initiate or make a change in regulatory action? The importance of the contri• Presented at the international symposium Human Health Aspects io Accidental Chemical Exposure
of Dicxir.s—S::aisgy for Environmental Reclamation snc Corr.mur.itv Protection, organized by the
International Academy of Environmental Safety (1AES) and the International Society of Ecotoxicolojy
and Er.viro.-.rncnta! Safety (SECOTOX) joiniiy with the Institute Superiore di Sanita. Rome, and the
Geseilschafrfur Strahien- und Umweh Forshung MbH, Munich.

379

o::?-::-oo;si/o:&gt;o379-o9so:.oo/o
Cc??Ti9i: 5 19M tv Academic Presi. Int
.Mi nf hu of rep.'odumor. in &gt;nv form reserved

�380

FRANK CORDLE

bution of epidemiology in the regulatory public health arena seems obvious. Without
adequate assessment of factors that appear"to increase the risk of disease in humans
from chemical substances in the food supply, food may be destroyed, the public
may be unnecessarily inconvenienced or inadequately protected, and the costs may
be enormous. In short, epidemiological efforts are directed toward the prediction
of such risk at the community, state, or national level.
It is quite likely that the majority of humans are exposed to a large number of
chemical substances in small amounts over an extended period of time rather than
to large doses such as those described in the mercury episode in Minamata or in
the PCB exposure in Japan. The importance of the possible cumulative effects from
these small doses versus the importance of the effects from a single large dose or
.from relatively large doses over a short period of time is the subject of considerable
scientific debate.
Much of the information concerning the toxicity of various chemical substances
has been obtained from experiments in animals. In general, safety testing depends
upon the fact that as the exposure dose is decreased, toxic effects also decrease,
and a dose is finally established at which "no observed effects" are seen. Such
dose-response relations are central to toxicity studies in animals and should be ef
equal concern in the evaluation of human exposure to a variety of environmental
and other insults. However, dose-response relations in humans must be established
or identified with a great deal of care and caution. Outcome may vary greatly in
significance: At one extreme is death and at the other are changes in physiological
or psychological function. The weight that should be given to each relation in
formulating regulatory policy may vary greatly.
The lack of good examples of dose-response 'relation, even in the area of occupational exposure, is remarkable. Where dramatic incidents of exposure to environmental contamination have occurred through ingestion of contaminated food,
efforts to establish an acceptable dose-response relation in humans have met with
little success.
However, epidemiologies! study should not be limited to outbreaks of disease
that are obviously caused by high exposures to toxic chemicals: it should be squally
concerned with the effects of lower, more prolonged, and sometimes insidious exposures.
EPIDEMIOLOGICAL METHODS
In the traditional manner, epidemiologists deal wi;h epidemics by interpreting
patterns of disease, testing hypotheses, and assessing the risks and benefits of various
options. Their methods involve the use of two categories of epidemiology often
referred to. as analytical and descriptive epidemiology. The analytical epidemiclogical methods generally involve either a case-control, retrospective approach or
a cohort, prospective approach.
In analytical epidemiology, the goal of epicsmioiogica! activity is to identify and.
if possible, to quantify the association between a cuusii exposure or characteristic
and a disease under circumstances that permit the best possible discrimination
between cause and aiternative hypotheses. Chance will always affect the alternatives: thus the feasibility of such a study is limited by factors such as sample size.

�EPIDEMIOLOGY AND REGULATION'OF D1OXINS

-"

381

Since a precise hypothesis permits the use of a well-thought-out and properly
planned study design, it is better to use the cohort approach to measure relative
and attributable risk, for example, than to try to detect trends from descriptive
data. Nevertheless, sample size considerations, cost, and time constraints often
restrict the kind of epidemiological study undertaken, even though the cohort approach might be preferred for a given problem.
Case-control studies of disease, i.e., studies looking at the past history of exposure,
are often more feasible than cohort studies because they can be conducted in a
relatively short time and are easily repeatable, and because a large number of cases
can be studied economically. They do have some special liabilities, however, in
terms of validity, since such studies depend entirely on the comparability of cases
and controls and on the specific methods used to measure the exposure. Although
frequently used, the methods for estimating relative risk or risk ratio from casecontrol studies also present some special problems of inference.
Cohort studies, i.e..-studies looking forward in time, are especially costly because
of the time involved in the prospective follow-up. They do, however, provide an
opportunity to compute a more reasonable relati%re and attributable risk, and specious relationships resulting from bias in data collection are less likely to occur.
Descriptive epidemioiogical methods can be used by a regulatory agency such
as FDA to determine trends in disease and magnitudes of exposed populations
largely from data that are readily available, e.g., mortality dau. data from National
Cancer Institute (NCI) surveys, census data, and food consumption data. The goal
of these studies is io identify any unexpected changes in incidents or.mortality
through surveillance of the available data for time trends and through probes of
specific data collected during research activities or gathered in support of regulatory
decisions.
Epidemiological studies also provide information that is used to identify and
quantify differences in species responsiveness to environmental agents in a variety
of other ways. One use. for example, pertains to the difficulty associated with
cornparir.c data derived from studies of highly inbred animal strains to data of a
genetically heterogeneous human population. In this case, epidemiological methodologies provide the means for stratification of study data according to sex, age,
race, and other variables that characterize human populations. Certain problems
rr.ay also be minimized when epiderniological considerations are employed in risk
assessments that are based on comparisons involving data of humans and data of
animal models. These include problems associated with limited sample sizes, znigra'.ior. in and out of the exposure area, and toxicity due to causes other than that
as-sociated Vjth exposure to the etioiogic agent under study.
EPIDEMIOLOGICAL AND TOXICOLOGICAL ASSESSMENT
OF TCDD EXPOSURE
Recent concern for the potential human health risk associated with exposure to
residues of the tetrachiorocibenzo-p-dioxins (TCDD) in several species of freshwater fish from various areas of the Greai Lakes has resulted in an epidemioiogical
arc toxicological assessment of the problem that utilizes currently available data
from a variety of data sets. For a regulatory decision to be made, several elements

�3S2

FRANK CORDLE

were needed. These included data for the TCDD residues in the freshwater fish,
for the amounts of the various fish species consumed and for the number of individuals who consumed the fish, and assessments of pertinent animal data and previous human exposure to TCDD.
Animal Data
A number of lexicological studies with TCDD have been conducted to assess
the potential for acute toxicity and teratogenesis. Kociba et al. (1976) reported the
results of a subchronic study using rats that were given 1.0, 0.1, 0.01, 0.001, or
0 /jg TCDD/kg body wt/day for 5 days/week for 13 weeks. Doses of 1.0 Mg TCDD/
kg/day caused some mortality, inactivity, decreased body weights and food consumption, pathornorphologic changes in the liver, lymphoid depletion of the thymus,
increased urinary excretion of porphyrins, and minimal alterations of some hematopoietic components. Doses of 0.1 ^g TCDD/kg/day caused decreased body
weights and food consumption and slight degrees of liver degeneration and lymphoid
depletion. These data indicate that no discernible ill effects occurred in rats given
0.01 or 0.001 jig TCDD/kg/day for 5 days/week for 13 weeks.
In a 2-year chronic study in rats Kociba et al. (1978) reported that the ingestion
of 0.1 ,ug TCDD/kg/day caused an increased incidence of hepatocellular carcinomas and squamous cell carcinomas of the lung, hard palate/nasal turbinates, or
tongue, whereas a reduced incidence of tumors of the pituitary, uterus, mammary
glands, pancreas, and adrenal glands was noted. Other indications of toxicity at
this dose level included increased mortality, decreased weight gain, slight depression
of erythroid parameters, and increased urinary excretion of porphyrins. Gross and
histopathologic charges were noted in the hepatic lymphoid. respiratory, and vascular '.issues. The primary hepatic ultrastructural change at this high dose level
was proliferation of the rough endopiasmic reticulum. Terminal liver and fat samples from rats given this high dose level contained 24.000 and S100 parts per trillion
(ppt) TCDD, respectively. Rats giver. 0.01 ng TCDD/kg/day for 2 years showed
less severe toxicological effects than those given the highest dose level. These included liver lesions (including hepstocellular nodules) and lung lesions (including
focal alveolar hyperplasia). Terminal liver and fat samples from rats given this
dose level contained 5100 and 1700 ppt TCDD, respectively. Ingestion of 0.001
yg TCDD/kg/day (22 ppt in the die;) caused no effects of any toxicological significance. Terminal liver and fat samples from rats given this low dose level each
confined 5-^0 ppt TCDD.
]- a 3-year reproduction study in rais given doss levels of 0. O.OOL 0.01, or 0.1
ug TCDD/'kg/day, Murray ei al. 'J979) reported no significant toxic effects in
the/c-ceneration rats of cither se.x curing the 90 days of TCDD ingestion prior to
': mating. However; significant decreases in fertility and neonatal survival were observed in the/o-generation rats receiving 0.1 ps TCDD/kg/day. At 0.01 Mg TCDD/
kg/day, fertility was significantly decreased in the/i and/ : generations, but not
in the/; generation, and decre55.es in litter size at birth, gestations! survival, and
neonatal survival and growth were also noted. Among the rats receiving 0.001 ^g
TCDD/kg/day, no effect on fertility. !i;:er &lt;ize at birth, or postnatal body weight
was observed in any generation. No consistent effect on neonatal survival was
observed at a dose level of 0.001 pg TCDD/kg/day. •

�EPIDEMIOLOGY AND REGULATION OF DIOXINS

383

Allen et al. (1977) reported results of a subchronic study in which female rhesus
monkeys consumed a diet containing 500 ppt TCDD for periods as long as 9 months.
It was calculated that these monkeys ingested a total of 2-3 Mg TCDD/kg body
wt over the course of the 9-month study. Clinically, these monkeys showed changes
similar to those described by McConnell et al. (1978) as well as some hematoiogic
depression and hemorrhages in various tissues. Hypertrophy, hyperplasia, and/or
metaplasia were noted in the epithelium of the bile ducts, salivary glands, bronchi,
pancreatic ducts, sebaceous glands, skin, gastric linings, and urinary tracts of these
monkeys given diets containing 500 ppt TCDD.
Human Experience
Alihough 22 incidents of human exposure to TCDD in connection with the
manufacture of chlorinated phenols have been reported worldwide since 1949
(Holmstedt, 1980). there remains a scarcity of reliable information concerning the
results of these exposures.
In a recent report of the mortality experience of a cohort of workers exposed to
TCDD in Nitro, West Virginia, in 1949. Zack and Suskind (1980) described some
of the signs and symptoms observed in the exposed population shortly, after the
accident occurred. Employees who-worked in the area of 2,4.5-trichlorophinol
(TCP) production or were involved in the cleanup began to develop symptoms
immediately following exposure to the material, which was discharged froir. the
autoclave. Symptoms included eye and respiratory tract irritation, headache, dizziness and nausea, and a severe irritant reaction of the exposed skin. After these
initial symptoms subsided, chioracne and other symptoms became evident. A total
of 12 more severely affected workers were examined or. three occasions during the
period 1949-1953. Another 26 persons with chioracne :hat was apparently unrelated to the accident were also examined in 1953.
The ciinical symptoms included acneform lesions: severe pains in muscles of
upper and lower extremities, shoulders, and thorax on exertion: fatigue: nervousness
and irritability: decrease in libido: dyspnea: vertigo: and intolerance to cole. All
of the cases showed evidence of chioracne. For the six workers examined curing
1949 and 1950. another examination was carried out in 1953. and at that time six
additional workers involved in the accident were also examined! The findings in
ihis later examination indicated a general regression of both the cutaneous and
ne.-cuiijriccus symptoms w h i c h had been present earlier. No specific leveis o; exposure could be determined.
In other reports of industrial exposure 10 TCDD frc.T. Great Britain, the Netherlands. \\fisi Germany, and Czechoslovakia, chioracne was the most common and
prominent sign observed following exposure. In some -sports liver function tests
indicated liver damage, whereas in other reports they die not. Two major problems
er.cour,:e:tc in all of these studies were the lack of 2. tltitr identification of •.hose
e.v-&lt;&gt;=d. other than their subsequent development of chioracne. and the absence
of any measures for the levels of exposure ihar might have taken place.
Pszdsrova-Vejlupkova et a!. ( 1 9 8 1 ) reported results of a 10-year follow-up study
of workers exposed ;o TCDD between 1965 snd 196s curing the production of
2.4.5-trichloropheno.xyacetic acid (2/,5-T). In this s t u d y group of 55 individuals

�384

FRANK CORDLE

(originally 80 of the 400 persons engaged in., the production became ill), the first
indications of illness were feelings of sickness, fatigue, weakness in the lower extremities, and the formation of chloracne. Subsequent examinations indicated that
about 20% had mild hepatic lesions.
During the 10-year follow-up study of these exposed individuals, most of the
patients did not experience all of the symptoms and signs of intoxication, and some
patients showed the same symptoms and signs as others, but in different combinations. It is assumed that in this type of intoxication all the systems and organs
mentioned in the study were simultaneously affected, although some were affected
only slightly. This assumption is supported by several facts. Fluorescence of liver
tissues in ultraviolet light, which is a sign of pathological porphyrin metabolism,
was present in all cases of necropsy and biopsy, i.e., in persons for whom long-term
monitoring of porphyrin excretion in urine was carried out and in whom 5-aminolevulinic acid values were constantly within normal limits'. Probably a slight
subclinical lesion was present in each of these patients. Further evidence was furnished in repeated neurological examinations. Polyneuropathy of the lower extremities was manifest in some patients only in the third or fourth year of illness. There
is definite clinical and electromyographic evidence that the results of the first examinations conducted when the illness commenced showed that the patients were
entirely normal.
Additional study results have been reported recently by Zack and Suskind 0980),
Ott et al. (1980), and Cook et al. (1980), describing ;hs mortality of employees
engaged in the manufacture of 2.4.5,-T. In two of these studies cohorts of employees
were assembled on the basis of their exposure to T.CDD. which was indicated,by
the presence of chloracne; the ihird cohort consisted of individuals employed over
the same time period. Unfortunately, each of these three cohorts comprised a
limited number of individuals: e.g., the chloracne groups contained 121 and 49
individuals and the employee group contained 204.
In each of these studies there does not appear to be an apparent excess in total
mortality rate or in deaths from malignant neoplasms. It must be pointed out,
however, that each of these studies does have limitations both in the size of the
population studied and in other methodological areas, such as exposure levels.
For a more detailed description of these studies as well as the Seveso incident,
the reader is referred to the original papers and to Hoimstect (1980), Reggiani
(19SO), and Pocchiari et al. (1979).
Hitman Exposure to TCDD Residues in Fish
Although there are no epidemiological studies which have firmly established an
association between cancer in humans and TCDD exposure, 2nd although comparisons of human exposure data and animal studies appear to indicate that humans
may be less sensitive than animals to TCDD exposure, prudence dictates that
human exposure to TCDD be kept to 3 minimum. With :h:s public health objective
ir. m;rd. FDA recently compieted an assessment of the problem of TCDD residues
in some species of freshwater fish in the Great Lakes for ;he purpose of determining
whether consumption of such fish provided a potential public health problem.
Results of the analyses of fish samples collected by Canada and the United States

�EPIDEMIOLOGY AND REGULATION OF D10XINS

-

385

TABLE i
HUMAN CONSUMPTION OF DIOXIN BASED ON FISH CONSUMPTION DATA
Total daily intake (ng*)

Total daily intake/body wt (pg'/kg)

From all selected
species

From all selected
species

Hypothetical
dioxin residue level
in fish consumed
(ppf)

90th
percentile

99th
percentile

From
pike, 99th
percentile

90th
percentile

99th
percentile

From
pike, 99th
percentile

100
SO
25

1.57
0.77
0.38

3.683
1.84
0.92

8.4
4.2
2.1

22
11
5.5

50
26
13

120
60
30

' ppt • pans per trillion.
" 1 microgram (»g) "..1000 nanograms (ng).
' 1 ng - 1000 picograms (pg).

indicated that TCDD levels as high as 30 ppt with an average value of 25 ppt were
present in the edible portion of salmonoid fish (salmon, trout) from. Lake Ontario.
Lower levels of TCDD were reported to be present in the edible portions of commercial species (bullhead, perch, catfish, sucker, etc.) from Lake Ontario^ although
up to 40 ppt TCDD were found in'eel and smelt from the lake. Less than 10 ppt
TCDD was seen in samples from Lake Erie, and limited data for_fish from the
other Great Lakes were similar to those obtained from Lake Erie fish, except that
higher levels of TCDD were present .in fish from Sagir.aw Bay, Michigan.
Data on fish consumption from the National Marine Fisheries Service (NMFS)
were extracted for the eight Great Lakes states, Illinois. Indiana. Michigan, Minnesota. New York, Ohio, Pennsylvania, and Wisconsin. These data were collected
in a national sample of households, consisting of approximately 25,000 individuals.
From the data presented, individuals who consumed the species of interest, i.e., the
species currently being analyzed for dioxin residues were identified in the total
sample, and the mean fish consumption, in grams per cay. was computed. The 90th
and 99th percentiles were also computed. On the basis of the proportion of individuals in the sample population consuming the species of interest, 17,057,791
individuals in the eight Great Lakes states would be expected to consume these
same species. It must be pointed out that the number of consumers in the total
population can be considered only ar. estimate because of the lack of information
on potential sampling error as well as other factors. These data indicated that the
99th percentile for daily consumption for all consumers of the selected species was
36.8 g; the 90th percentile for daily consumption was 15.7 g. For a single species
of fish such as pike, which appeared to be consumed in larger amounts than all the
species combined, the 99th percentile of consumption was 83.95 g. Table 1, which
is based on these fish consumption data, shows :he daily human consumption for
a range of hypothetical dioxin residue levels.
Thus, the four elements of the model for a scisn::f.c regulatory assessment, i.e.,
animal data, human data, consumption data, and residue data, were available. In
this instance the h u m a n data concerning TCDD exposure contributed little to the
regulatory decision because of the uncertainty of the exposure data as well as the

�386

FRANK CORDLE

uncertainty of the outcome of the exposure. It was necessary, therefore, to rely on
extrapolation from animal to human. In this case the rodent data from the 2-year
chronic feeding study (Kociba ei a/., 1978) were used for the extrapolation.
Results of that study showed that
(a) at 0.001 Mg/kg body wt/day, no adverse effects were noted in rats exposed
for their lifetimes to the dioxin;
(b) at 0.01 ng/kg body wt/day, hyperplasia of the liver and lung was observed
to occur, thus indicating an observable effect related to enzyme induction and liver
cell response to the compound;
(c) at 0.1 Mg/kg body wt/day, an increase in liver carcinomas was observed.
The animal-to-human extrapolation of the no-effect level for TCDD exposure
from the rodent data indicated an intake of 1 ng/'kg body wt/dav or a total daily
intake of 70 ng as the no-effect level. If fish containing average TCDD residue
levels of 25 ppt were consumed in the amount of the 99th percentile. i.e., 36.8 g/'
day. the total daily intake of TCDD would be 0.92 ng or 13 pg/kg body wt/day
or less than l/70th of the no-effect level, less than 1/700th of the lowest-effect
level, and less than 1 /7000th of the carcinogenic level. The safety margin at the
90th percentile of consumption is even greater.
As a result of this assessment, a public health advisory was sent to the health v
officers in each of the Great Lakes states, encouraging a continued mor.itoring of
TCDD residues in fish, especially in certain local areas where TCDD levels mightbe higher than the average, and where Local fish consumption might also be higher
than that for the Great Lakes area as a whole.
This exa.r.ple in regulatory decision making illustrates FDA's role in protecting
public health by ensuring a safe and nutritious food'supply. This responsibility is
exercised by individuals who call upon science, law, and the regulatory process to
accommodate the demands of safety, contamination, food requirements, Congress,
consumers, and the courts. Although the regulatory process has often been criticized, on the whole it has provided effective public health protection for the millions
who consume food in the United States.
REFERENCES
ALLEN. J. R.. BARSOTT;. D. A.. VAN MILLER, J. P., ABRAHAMSOS. L. L. AND LAUGH. J. J. 09").
Mcrp'-oiogica! changes in monkeys consuming a diet co.-.;aining low isvsis of ;.3.~.S-tei:ichlorodiber.io-p-c'ioxin. Food Cosmct. Toxicol. IS, 401-410.
COOK. R. R.. TOWNSEND. J. C. OTT. M. G.. AND SILVERSTEIN. L. B. (!9SO). Mor.a!h&gt; experience
. cf srspic.yeej exposed to :.j.T.S-ieirachioro&lt;Jib«.-i20-..--cio.\ir.. JO.'.f J. 0^-ap. .'•'&lt;::. 21. &lt;3C-&lt;21
HOLMSTSCT. B. 119SO). Prolegomena to Scveso. Arch. Toxicoi. 44. :i l-:;-0.
KOC:SA. R. J.. KsELER. P. A.. PARK. C. N.. AND GEMMING. P. J. H976). 13.7.&amp;-7j',ri:hic-:ociber.:op-cio.\in (TCDD;: Results of a 13-week orii loxiciiy s;udy in rats. Toxicol. Appl. Phsrn-.acol. 35,

553-574.
KOCISA. R. 1. KEYSS, D. G.. SEVER.-J. E.. CARRSON, R. M.. \VADE. C. £.. DITTENJIER, D. A..
KALMNS. R. ?.. FRACSON. L. E., PARK. C. N.. BARNARD. S. D.. HUMMEL, R. A.. AND HCMISTOS.

C. G. ('197*1. Results of a two-year chronic :oxic::y and oncng«riici:y jiucy o.f ;.3.7.S-;e::s&gt;ch!oro•iiber.io-p-dicxir. i.-..ra:s. Tbxifol. .*.,-,"!. Pksrmecol. 46. "9-?03,
McCosvaiJ.. £. E.. .'MOORE. J. A., AND DALOARO. D. W. (197S). Toxicity of :,3.7.S-ie:;achlorocibcr.^o-/i-cioxin (TCDD) ir. rhesus rnonl.eys (Macaco mvlci;a'i follow, jr.; 2 sir.gie orai dose. Toxieol.
Af-p!. Pns.'rr.cto!. 43, 175-187.
MUKP.AV. F.. J.. SMITH. F. A., SITSCHKE. K. D., HAMESTON. C. G., KocibA. R. J., AVD SC.HWETZ.

�EPIDEMIOLOGY AND REGULATION OF D10XINS

387

B. A. (.1979). Three-generation reproduction study of rats given 2.3,7.8-ietrachlorodibenzo-p-dioxin
(TOO! ir. '.he diet. Toxicol. Appl. Pharmacol. 50, 24J-252.
Orr. M. G.. HOLDER, B. B., AND OLSON. R. D- (1980). A mortality analysis of employees engaged
ir. the manufacture of 2.4,5-trichlorophenoxy acetic acid. JOM J. Occup. Mtd. 22. 47-50.
PA2DsROVA-V£JLUTKOv.v J.. NgWCOVA. M., PlCKOVA. J.. JlRASEK. L, AND LUKAS. E. (1981). The

oeveiopmem and prognosis of chronic intoxication by t«rachlorodibenzo-/&gt;-dioxin in men. Arch. En\-iror.. Heolih 36, 5-11.
PoccHiARi. F., SILANO. V., AND ZAMPIERI. A. (1979). Human health effects from accidental release
of tetrachlorodibenzo-p-dioxins (TCDD) a; Seveso. Italy. Ann. N. Y. Acad. Sci. 320, 311-320.
RECC:AM, G. U9SO). Acute human exposure to TCDD in Seveso, Italy. / Toxicol. Environ. Health
6, 2?-43.
ZACK. J. A.. AND SUSKIND. R. R. (1980). The mortality experience of workers exposed to tetrachiorodibenzodioxin in a trichlorophenol process accident. JOM J. Occup. Med. 22, 11-14.

�f. CooiU
Ajril H, t ^ S
PCOD INTAKE FOR DIOXIN, PCP LEVELS OF OONCESN

18-45yrs 2-5yrs
bw.71.2 bw.16.3

total red neat and poultry
Ibtal red meat

212g
108g

109.6g

Beef

134g

65.6g

Veal
Beef + veal

20g
136g

Lairb + mutton
Beef liver

17g
20g

Pork
Pork (45-64 years)

67g
75g

36^3g

8g

6.7

Pork liver
Poultry (total)
Poultry (total; 45-64 years)
Chicken
Chicken (45-64 years) -.•
Chicken liver
Turkey
Duck

'

53g
56g
44g
47g
13g
33g
17g

25.4g
4.4g'

Eggs
Ecgs( 45-64 years)

47g
58g

28.5g

Milk fat
Milk fat( 13-17 years)
Non-fat
railk
Ken-fat milk (13-17 years)

24g
31g
48g
74g

23.4g

�Samples collected fron Smith Farms (26 operating farms) en 1/17/83
Eggs
Eggs
Eggs
Eggs

- Farm £34
- K&amp;M Farm
- Farm #40
- Benders Farm

0.20ppm (PCP)
O.lSpcm (PC?)
O.~13ppm (PCP)

Feed
Feed
Feed

0.26ppn (PC?)

Feed

O.OSppm (PC?
0.07ppra (PC?)
Trace (PCP) .
Trace (PCP)

Food consumotion bv days and meals:
Beef
Perk
Chicken
Eggs
Milk fat
Other

18-45 years
134g X 5 ireals=670g
75g X 5 neals=375g
44g X 4 meals=176g
47g X 7 msals=329g
24g X 7 iTBals=168g

30g X 7 neals»210g

1928g

1928g/7=275.4g/day

2-5 years
55.6g X 5 meals=328c
36.3g X 5 neals=182g
25.4g X 4 m=alssl02g
.28.5g X 7 meals=200g
.23.4g X 7 nfials=174g
10.Og X 7 maals-TO^
1056c
1056g/7=151g/day

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                  <text>Alvin L. Young Collection on Agent Orange</text>
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                  <text>&lt;p style="margin-top: -1em; line-height: 1.2em;"&gt;The Alvin L. Young Collection on Agent Orange comprises 120 linear feet and spans the late 1800s to 2005; however, the bulk of the coverage is from the 1960s to the 1980s and there are many undated items. The collection was donated to Special Collections of the National Agricultural Library in 1985 by Dr. Alvin L. Young (1942- ). Dr. Young developed the collection as he conducted extensive research on the military defoliant Agent Orange. The collection is in good condition and includes letters, memoranda, books, reports, press releases, journal and newspaper clippings, field logs and notebooks, newsletters, maps, booklets and pamphlets, photographs, memorabilia, and audiotapes of an interview with Dr. Young.&lt;/p&gt;&#13;
&lt;p&gt;For more about this collection, &lt;a href="/exhibits/speccoll/exhibits/show/alvin-l--young-collection-on-a"&gt;view the Agent Orange Exhibit.&lt;/a&gt;&lt;/p&gt;</text>
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        <element elementId="52">
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              <text>1353</text>
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            <elementText elementTextId="16582">
              <text>Series III Subseries II</text>
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              <elementText elementTextId="16578">
                <text>Barnes, Donald G.</text>
              </elementText>
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                <text>Memorandum: FDA Risk Assessment for Higher Chlorinated Dibenzo-p-dioxins, from Donald G. Barnes to Alvin Young and others, May 13, 1983</text>
              </elementText>
            </elementTextContainer>
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          <element elementId="49">
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                <text>dioxin</text>
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                <text>dietary exposure</text>
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                <text>animal testing</text>
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