Document ID: EPA-HQ-OPPT-2016-0770-0001
Agency: epa
Document Type: Proposed Rule
Title: TSCA Section 21 Petition; Reasons for Agency Response: Tetrabromobisphenol A (TBBPA)
Posted Date: 2017-03-17T04:00Z

[Federal Register Volume 82, Number 51 (Friday, March 17, 2017)]
[Proposed Rules]
[Pages 14171-14184]
From the Federal Register Online via the Government Publishing Office [www.gpo.gov]
[FR Doc No: 2017-05291]

-----------------------------------------------------------------------

ENVIRONMENTAL PROTECTION AGENCY

40 CFR Chapter I

[EPA-HQ-OPPT-2016-0770; FRL-9960-09]

Tetrabromobisphenol A (TBBPA); TSCA Section 21 Petition; Reasons 
for Agency Response

AGENCY: Environmental Protection Agency (EPA).

ACTION: Petition; reasons for Agency response.

-----------------------------------------------------------------------

SUMMARY: This document provides the reasons for EPA's response to a 
petition it received under the Toxic Substances Control Act (TSCA). The 
TSCA section 21 petition was received from Earthjustice, Natural 
Resources Defense Council, Toxic-Free Future, Safer Chemicals, Healthy 
Families, BlueGreen Alliance, and Environmental Health Strategy Center 
on December 13, 2016. The petitioners requested that EPA issue an order 
under TSCA section 4, requiring that testing be conducted by 
manufacturers (which includes importers) and processors on 
tetrabromobisphenol A (``TBBPA'') (CAS No. 79-94-7). After careful 
consideration, EPA denied the TSCA section 21 petition for the reasons 
discussed in this document.

DATES: EPA's response to this TSCA section 21 petition was signed March 
10, 2017.

FOR FURTHER INFORMATION CONTACT: 
    For technical information contact: Virginia Lee, Chemical Control 
Division (7405M), Office of Pollution Prevention and Toxics, 
Environmental Protection Agency, 1200 Pennsylvania Ave. NW., 
Washington, DC 20460-0001; telephone number: (202) 564-4142; email 
address: lee.virginia@epa.gov.
    For general information contact: The TSCA-Hotline, ABVI-Goodwill, 
422 South Clinton Ave., Rochester, NY 14620; telephone number: (202) 
554-1404; email address: TSCA-Hotline@epa.gov.

SUPPLEMENTARY INFORMATION: 

I. General Information

A. Does this action apply to me?

    This action is directed to the public in general. This action may, 
however, be of interest to those persons who are or may manufacture 
(which includes import) or process the chemical tetrabromobisphenol A 
(``TBBPA'') (CAS No. 79-94-7). Since other entities may also be 
interested, the Agency has not attempted to describe all the specific 
entities that may be affected by this action.

B. How can I access information about this petition?

    The docket for this TSCA section 21 petition, identified by docket 
identification (ID) number EPA-HQ-OPPT-2016-0770, is available at 
http://www.regulations.gov or at the Office of Pollution Prevention and 
Toxics Docket (OPPT Docket), Environmental Protection Agency Docket 
Center (EPA/DC), West William Jefferson Clinton Bldg., Rm. 3334, 1301 
Constitution Ave. NW., Washington, DC. The Public Reading Room is open 
from 8:30 a.m. to 4:30 p.m., Monday through Friday, excluding legal 
holidays. The telephone number for the Public Reading Room is (202) 
566-1744, and the telephone

[[Page 14172]]

number for the OPPT Docket is (202) 566-0280. Please review the visitor 
instructions and additional information about the docket available at 
http://www.epa.gov/dockets.

II. TSCA Section 21

A. What is a TSCA section 21 petition?

    Under TSCA section 21 (15 U.S.C. 2620), any person can petition EPA 
to initiate a rulemaking proceeding for the issuance, amendment, or 
repeal of a rule under TSCA section 4, 6, or 8 or an order under TSCA 
section 4 or 5(e) or (f). A TSCA section 21 petition must set forth the 
facts that are claimed to establish the necessity for the action 
requested. EPA is required to grant or deny the petition within 90 days 
of its filing. If EPA grants the petition, the Agency must promptly 
commence an appropriate proceeding. If EPA denies the petition, the 
Agency must publish its reasons for the denial in the Federal Register. 
A petitioner may commence a civil action in a U.S. district court to 
compel initiation of the requested rulemaking proceeding within 60 days 
of either a denial or the expiration of the 90-day period.

B. What criteria apply to a decision on a TSCA section 21 petition?

    1. Legal standard regarding TSCA section 21 petitions. Section 
21(b)(1) of TSCA requires that the petition ``set forth the facts which 
it is claimed establish that it is necessary'' to issue the rule or 
order requested. 15 U.S.C. 2620(b)(1). Thus, TSCA section 21 implicitly 
incorporates the statutory standards that apply to the requested 
actions. Accordingly, EPA has relied on the standards in TSCA section 
21 and in the provisions under which actions have been requested to 
evaluate this TSCA section 21 petition. In addition, TSCA section 21 
establishes standards a court must use to decide whether to order EPA 
to initiate rulemaking in the event of a lawsuit filed by the 
petitioner after denial of a TSCA section 21 petition. 15 U.S.C. 
2620(b)(4)(B).
    2. Legal standard regarding TSCA section 4 rules. EPA must make 
several findings in order to issue a rule or order to require testing 
under TSCA section 4(a)(1)(A)(i). In all cases, EPA must find that 
information and experience are insufficient to reasonably determine or 
predict the effects of a chemical substance on health or the 
environment and that testing of the chemical substance is necessary to 
develop the missing information. 15 U.S.C. 2603(a)(1). In addition, EPA 
must find that the chemical substance may present an unreasonable risk 
of injury under section 4(a)(1)(A)(i). Id. If EPA denies a petition for 
a TSCA section 4 rule or order and the petitioners challenge that 
decision, TSCA section 21 allows a court to order EPA to initiate the 
action requested by the petitioner if the petitioner demonstrates to 
the satisfaction of the court by a preponderance of the evidence in a 
de novo proceeding that findings very similar to those described in 
this unit with respect to a chemical substance have been met.

III. Summary of the TSCA Section 21 Petition

A. What action was requested?

    On December 13, 2016, Earthjustice, Natural Resources Defense 
Council, Toxic-Free Future, Safer Chemicals, Healthy Families, 
BlueGreen Alliance, and Environmental Health Strategy Center petitioned 
EPA to issue an order under TSCA section 4(a)(1), 90 days after the 
petition was filed, requiring that testing be conducted by 
manufacturers (which includes importers) and processors on 
tetrabromobisphenol A (``TBBPA'') (CAS No. 79-94-7) (Ref. 1).

B. What support do the petitioners offer?

    The petitioners state section 4(a)(1) of TSCA requires EPA to 
direct testing on a chemical substance or mixture if it finds the 
following criteria are met:
    1. The manufacture, distribution in commerce, processing, use, or 
disposal of a chemical substance or mixture, or that any combination of 
such activities, may present an unreasonable risk of injury to health 
or the environment.
    2. There is insufficient information and experience upon which the 
effects of such manufacture, distribution in commerce, processing, use, 
or disposal of such substance or mixture, or of any combination of such 
activities on health or the environment can reasonably be determined or 
predicted.
    3. Testing is necessary to develop such information.
    The petitioners assert that TBBPA ``may present an unreasonable 
risk of injury to health or the environment'' because there is 
substantial evidence that TBBPA may be toxic, including conclusions 
from:
     EPA's TSCA Work Plan Chemical Problem Formulation and 
Initial Assessment (Ref. 2), which states TBBPA ``can be considered 
hazardous to the environment'' and that ``there is some concern'' for 
certain cancers and developmental effects.
     The International Agency for Research on Cancer (IARC) has 
identified TBBPA as probably carcinogenic to humans (Ref. 3).
     Multiple in vitro and animal tests, where TBBPA has been 
detected to cause endocrine effects, reproductive effects, neurological 
effects, and immunological effects (Refs. 4-9).
    The petitioners also note that EPA, upon adding TBBPA in 1999 to 
the Toxics Release Inventory (TRI) established under the Emergency 
Planning and Community Right to Know Act, concluded that ``TBBPA is 
toxic'' because ``[i]t has the potential to kill fish, daphnid, and 
mysid shrimp, among other adverse effects, based on chemical and/or 
biological interactions.'' 64 FR 58666, 58708. The petitioners assert 
there is TBBPA exposure to humans and the environment based on the 
following conclusions.
     TBBPA has the highest production volume of any brominated 
flame retardant and is extensively used in consumer products, including 
children's products (Ref. 2). The potential for widespread exposure is 
extremely high.
     In 2012, TRI indicated that 127,845 pounds of TBBPA were 
released into the environment (Ref. 2). Such releases indicate the 
potential for widespread exposure in the population.
     The presence of TBBPA in people and the environment (biota 
and environmental media) is established and affirmed in EPA's TBBPA 
Problem Formulation and Initial Assessment (Ref. 2).
    With the evidence of toxicity and exposure and EPA's addition of 
TBBPA to TRI (Ref. 10), the petitioners argue that TBBPA clearly meets 
the TSCA section 4 criteria for ``may present an unreasonable risk of 
injury to health or the environment.''
    The petitioners also assert there is ``insufficient information'' 
on TBBPA based on EPA's TBBPA Problem Formulation (Ref. 2), which 
petitioners say cited lack of data for:
     Dermal and inhalation exposures, diet and drinking water 
exposures, exposures to communities near facilities that manufacture 
and process TBBPA, exposures to communities near facilities where ``e-
waste'' is disposed of and recycled, exposures to the workers in 
manufacturing, processing, disposal and recycling facilities, and 
exposures to degradation and combustion products.
     developmental, reproductive and neurological toxicity, 
endocrine disruption, and genotoxic effects.
    The petitioners argue that the testing recommended in the petition 
is critical to address this allegedly insufficient information and for 
performing any TSCA section 6 risk evaluation of TBBPA, and they 
request EPA to not

[[Page 14173]]

commence the risk evaluation for TBBPA until data generated to comply 
with the section 4 test order requested by the petitioners have been 
received by EPA.

IV. Disposition of TSCA Section 21 Petition

A. What was EPA's response?

    After careful consideration, EPA has denied the petition. A copy of 
the Agency's response, which consists of two letters to the signatory 
petitioners from Earthjustice and Natural Resources Defense Council 
(Ref. 11), is available in the docket for this TSCA section 21 
petition.

B. Background Considerations for the Petition

    EPA published a Problem Formulation and Initial Assessment for 
TBBPA in August 2015 (Ref. 2). As stated on EPA's Web site titled 
``Assessments for TSCA Work Plan Chemicals'' (Ref. 12), ``As a first 
step in evaluating TSCA Work Plan Chemicals, EPA performs problem 
formulation to determine if available data and current assessment 
approaches and tools will support the assessments.'' During development 
of the Problem Formulation and Initial Assessment document for TBBPA, 
EPA followed an approach developed for assessing chemicals under TSCA 
as it existed at that time.
    Under TSCA prior to the June amendments, EPA performed risk 
assessments on individual uses, hazards, and exposure pathways. The 
approach taken during the TSCA Work Plan assessment effort was to focus 
risk assessments on those conditions of use that were most likely to 
pose concern, and for which EPA identified the most robust readily 
available, existing, empirical data, located using targeted literature 
searches, although modeling approaches and alternative types of data 
were also considered. EPA relied heavily on previously conducted 
assessments by other authoritative bodies and well-established 
conventional risk assessment methodologies in developing the Problem 
Formulation documents. Although EPA identified existing data and 
presented them in the problem formulations, EPA did not necessarily 
undertake a comprehensive search of available data or articulate a 
range of scientifically supportable approaches that might be used to 
perform risk assessment for various uses, hazards, and exposure 
pathways in the absence of directly applicable, empirical data prior to 
seeking public input. Rather, EPA generally elected to focus its 
attention on the uses, hazards, and exposure pathways that appeared to 
be of greatest concern and for which the most extensive relevant data 
had been identified. (Ref. 2).
    As EPA explains on its Web site, ``Based on on-going experience in 
conducting TSCA Work Plan Chemical assessments and stakeholder 
feedback, starting in 2015 EPA will publish a problem formulation for 
each TSCA Work Plan assessment as a stand-alone document to facilitate 
public and stakeholder comment and input prior to conducting further 
risk analysis. Commensurate with release of a problem formulation 
document, EPA will open a public docket for receiving comments, data or 
information from interested stakeholders. EPA believes publishing 
problem formulations for TSCA Work Plan assessments will increase 
transparency of EPA's thinking and analysis process, provide 
opportunity for public/stakeholders to comment on EPA approach and 
provide additional information/data to supplement or refine assessment 
approach prior to EPA conducting detailed risk analysis and risk 
characterization.'' (Ref. 12).
    EPA's 2015 Problem Formulation and Initial Assessment for TBBPA 
does not constitute a full risk assessment for TBBPA, nor does it 
purport to be a final analysis plan for performing a risk assessment or 
to present the results of a comprehensive search for available data or 
approaches for conducting risk assessments. Rather, it is a preliminary 
step in the risk assessment process, which EPA desired to publish to 
provide transparency and the opportunity for public input. EPA received 
comments from Earthjustice, Natural Resources Defense Council and 
others during the public comment period, which ended in November 2015 
(Ref. 13). After the public comment period, EPA was in the process of 
considering this input in refining the analysis plan and further data 
collection for conducting a risk assessment for TBBPA.
    On June 22, 2016, Congress passed the Frank R. Lautenberg Chemical 
Safety for the 21st Century Act. EPA has interpreted the amended TSCA 
as requiring that forthcoming risk evaluations encompass all 
manufacturing, processing, distribution in commerce, use, and disposal 
activities that the Administrator determines are intended, known, or 
reasonably foreseen (Ref. 14). This interpretation, encompassing 
``conditions of use'' as defined by TSCA section 3(4), has prompted EPA 
to re-visit the scoping and problem formulation for risk assessments 
under TSCA. Other provisions included in the amended TSCA, including 
section 4(h) regarding alternative testing methods, have also prompted 
EPA to evolve its approach to scoping and conducting risk assessments. 
The requirement to consider all conditions of use in risk evaluations--
and to do so during the three to three and a half years allotted in the 
statute--has led EPA to more fully evaluate the range of data sources 
and technically sound approaches for conducting risk evaluations. Thus, 
a policy decision articulated in a problem formulation under the pre-
amendment TSCA not to proceed with risk assessment for a particular 
use, hazard, or exposure pathway does not necessarily indicate at this 
time that EPA will need to require testing in order to proceed to risk 
evaluation. Rather, such a decision indicates an area in which EPA will 
need to further evaluate the range of potential approaches--including 
generation of additional test data--for proceeding to risk evaluation. 
EPA is actively developing and evolving approaches for implementing the 
new provisions in amended TSCA. These approaches are expected to 
address many, if not all, of the data needs asserted in the petition. 
Whereas under the Work Plan assessment effort, EPA sometimes opted not 
to include conditions of use for which data were limited or lacking, 
under section 6 of amended TSCA, EPA will evaluate all conditions of 
use and will apply a broad range of scientifically defensible 
approaches--using data, predictive models, or other methods--that are 
appropriate and consistent with the provisions of TSCA section 26, to 
characterize risk and enable the Administrator to make a determination 
of whether the chemical substance presents an unreasonable risk.

C. What was EPA's reason for this response?

    For the purpose of making its decision on the response to the 
petition, EPA evaluated the information presented or referenced in the 
petition and its authority and requirements under TSCA sections 4 and 
21. EPA also evaluated relevant information that was available to EPA 
during the 90-day petition review period that may have not been 
available or identified during the development of EPA's TBBPA Problem 
Formulation and Initial Assessment (Ref. 2).
    EPA agrees that the manufacture, distribution in commerce, 
processing, use, or disposal of TBBPA may present an unreasonable risk 
of injury to health

[[Page 14174]]

or the environment under TSCA section 4(a)(1)(A). EPA also agrees that 
the Problem Formulation and Initial Assessment was not comprehensive in 
scope with regard to the conditions of use of TBBPA, exposure pathways/
routes, or potentially exposed populations. However, the Problem 
Formulation and Initial Assessment was not designed to be 
comprehensive. Rather, the Problem Formulation and Initial Assessment 
was developed under EPA's then-existing process, as explained 
previously. It was a fit-for-purpose document to meet a TSCA Work Plan 
(i.e., pre-Lautenberg Act) need. Going forward under TSCA, as amended, 
EPA will conform its analyses to TSCA, as amended. EPA has explained 
elsewhere how the Agency proposes to conduct prioritization and risk 
evaluation going forward (Refs. 15 and 16). However, EPA does not find 
that the petitioners have demonstrated, for each exposure pathway and 
hazard endpoint presented in the petition, that the existing 
information and experience available to EPA are insufficient to 
reasonably determine or predict the effects on health or the 
environment from ``manufacture, distribution in commerce, processing, 
use, or disposal'' of TBBPA (or any combination of such activities) nor 
that the specific testing they have identified is necessary to develop 
such information.
    The discussion that follows provides the reasons for EPA's decision 
to deny the petition based on the finding for each requested test that 
the information on the individual exposure pathways and hazard 
endpoints identified by the petitioners does not demonstrate that there 
is insufficient information upon which the effects of TBBPA can 
reasonably be determined or predicted or that the requested testing is 
necessary to develop additional information. The sequence of EPA's 
responses follows the sequence in which requested testing was presented 
in the petition (Ref. 1).
    1. Dermal and Inhalation Exposure Toxicity. a. Dermal toxicity. The 
petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict effects to health from dermal exposure to TBBPA. Therefore, the 
toxicokinetics test (Organisation for Economic Co-operation (OECD) Test 
Guideline 417) (Ref. 17) via the dermal route and the skin absorption: 
In vivo test (OECD Test Guideline 427) (Ref. 18), requested by the 
petitioners, are not needed. The information already available includes 
oral toxicity studies and oral toxicokinetic studies identified in 
EPA's Problem Formulation and Initial Assessment document (Ref. 2) and 
the dermal toxicokinetics study identified by the petitioners (Ref. 
19). These available studies are sufficient to reasonably determine the 
internal doses of TBBPA for purposes of route-to-route (oral to dermal) 
extrapolation. The 2016 Yu et al. study, cited in the petition (Ref. 
1), characterizes absorption and elimination, while distribution and 
metabolism characterization is available from studies using intravenous 
dosing (Ref. 20). Furthermore, the available studies do not indicate 
differential distribution, metabolism, and elimination specific to 
skin. Therefore, the dermal toxicokinetics study requested by the 
petitioners is not needed to inform or refine evaluation of dermal 
exposures.
    b. Inhalation toxicity. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict effects to health from inhalation 
exposure to TBBPA. Therefore, the toxicokinetics test (OECD Test 
Guideline 417) (Ref. 17) via the inhalation route, requested by the 
petitioners, is not needed. As described in EPA's Problem Formulation 
and Initial Assessment (Ref. 2), EPA will use an alternative approach 
to evaluate risks from inhalation exposure to TBBPA. Because TBBPA is a 
solid, it may be reasonably predicted that particulates in the air are 
the primary form of TBBPA that would be inhaled. TBBPA particles in air 
that are inhaled are subsequently swallowed via the mucociliary 
escalator (Ref. 21). Once the particles are in the gastrointestinal 
tract, absorption can reasonably be assumed to be the same as in the 
oral toxicity studies and hence, oral toxicity studies can be used for 
risk assessment. Information is also available to estimate 
bioaccessibility of TBBPA from dust using an extraction test with an in 
vitro colon (Ref. 22). This additional information could also be 
considered when evaluating risks from TBBPA via the oral route. This 
approach would not require conducting the requested toxicokinetics test 
(Ref. 17).
    Although a small percent of TBBPA particles may be in the 
respirable range and may be absorbed directly through the lungs, 
existing tests show that no systemic effects were observed in a 14-day 
inhalation toxicity study (Ref. 23). Therefore, EPA considers that 
assuming all inhaled particles are eventually swallowed and using 
existing oral toxicity data should not underestimate effects from 
inhaling TBBPA particles and therefore would reasonably predict such 
effects.
    Furthermore, EPA's use of available existing toxicity information 
reduces the use of vertebrate animals in the testing of chemical 
substances in a manner consistent with provisions described in TSCA 
section 4(h).
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict effects to the environment, specifically, toxicity to plants 
exposed to TBBPA via the air. Therefore, the early seedling growth 
toxicity test (OCSPP Test Guideline 850.4230) (Ref. 24), requested by 
the petitioners, is not needed. As previously mentioned, because TBBPA 
is a solid, it may be reasonably predicted that particulates in the air 
are the primary form of TBBPA that would exist in air. Furthermore, as 
stated on page 88 of EPA's Problem Formulation and Initial Assessment 
document (Ref. 2), ``[u]ltimately air releases of TBBPA would be 
expected to undergo deposition to terrestrial and aquatic environments 
. . .'' and ``TBBPA tends to partition to soil and sediment . . .''. 
These fate pathways for TBBPA are also shown in Figure 2-1 of EPA's 
Problem Formulation and Initial Assessment document (Ref. 2). Hence, 
exposure of plants to TBBPA is expected to occur primarily via soil and 
sediments after deposition from air, which is why EPA excluded this 
pathway from further assessment (Ref. 2, page 42), although EPA in the 
Problem Formulation and Initial Assessment document mistakenly 
mentioned plants in another sentence addressing ``[e]xposure via 
directly inhaling [emphasis added] TBBPA,'' even though direct 
inhalation is not applicable to plants and thereby may have caused 
potential confusion to readers. If toxicity of TBBPA to plants were to 
be included in an assessment, toxicity data following exposure via soil 
and/or sediment exposures, not air, would be the scientifically 
relevant data needed. To this end, as described in EPA's Problem 
Formulation and Initial Assessment (Ref. 2), existing data and 
information on phytotoxicity of TBBPA to six plant species is available 
(Ref. 25). EPA's Problem Formulation and Initial Assessment document 
(Ref. 2) included references for and a brief description of the 
existing plant toxicity data (page 105). While assessment of soil-
dwelling organisms is included in EPA's Problem Formulation and Initial 
Assessment document (Ref. 2), as depicted in Figure 2-1 and described 
on page 40, EPA indicated that the environmental risk assessment for 
the soil exposure pathway would be based on concentrations of concern 
derived from data for soil invertebrates (Ref. 2; Figure 2-1; Table 2-
6; Page 40). Support for

[[Page 14175]]

EPA's selection of using species that are expected to be more sensitive 
to potential effects of TBBPA in soil is provided in EPA's summary of 
plant toxicity data, which states ``. . . TBBPA is two to three orders 
of magnitude less toxic to terrestrial plants than to soil-dwelling 
organisms'' (Ref. 2; Table_Apx F-2 and text on page 106).
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict toxicity of TBBPA to avian species. Hence, inhalation 
toxicokinetic studies (OECD Test Guideline 417) (Ref. 17) and the acute 
inhalation toxicity study (OCSPP Test Guideline 870.1300) (Ref. 26) 
modified for birds, requested by the petitioners, are not needed. 
Although the Problem Formulation and Initial Assessment document 
states, ``Exposure via directly inhaling TBBPA will not be assessed 
because no information is available on the toxicity of 
tetrabromobisphenol A to plants and other wildlife organisms (e.g., 
birds) exposed via the air.'' (Ref. 2; page 42), EPA's primary 
rationale for not including further elaboration of inhalation risks to 
avian species, as discussed in the Problem Formulation and Initial 
Assessment document (Ref. 2; page 32 and Appendix F) is TBBPA's low 
avian toxicity demonstrated in existing studies.
    Halldin et al., 2001 and Berg et al., 2001 (Refs. 27 and 28) 
indicate no effects to egg-laying female quail nor embryos (except at 
very high doses). The Halldin et al. (Ref. 27) study also included 
toxicokinetic data indicating that TBBPA is rapidly metabolized and 
excreted in birds (both embryos and egg-laying females). In these 
studies, TBBPA was delivered by intravenous injection into females and 
direct injection into eggs. This dosing regimen assures full (100%) 
delivery of the dose into the animal, which does not occur in nature, 
and thus provides the most sensitive means to detect the toxicity of 
the TBBPA. Other routes of exposure (i.e., oral, inhalation, dermal) 
result in incomplete absorption limiting the systematic availability of 
TBBPA compared to the intravenous injection (i.e., less than 100% 
delivered dose). Hence, intravenous toxicity test designs provide a 
good understanding of the potential toxicity (or lack thereof) of a 
chemical. In addition to the low avian toxicity of TBBPA, demonstrated 
via intravenous injection, inhalation is not expected to be a 
substantial exposure pathway to wildlife for TBBPA (Refs. 29 and 30). 
The predominant route of exposure to terrestrial wildlife for a 
chemical with physical-chemical properties (i.e., Log KOW = 
5.90; water solubility = 4.16 mg/L) and partitioning parameters (i.e., 
low mobility in soil) such as TBBPA is not expected to be via 
inhalation, but rather through ingestion because the TBBPA will 
predominantly partition to soils and sediments if/when released to the 
environment. The physical-chemical properties of TBBPA also indicate 
that the fate of TBBPA into water would result in preferential 
partitioning into sediments and biota (fish or other aquatic organism). 
Available monitoring data support this conclusion, with higher 
concentrations of TBBPA in soil and fish relative to concentrations in 
air.
    Hence, additional toxicokinetic studies by the inhalation route is 
not needed to conduct a reasoned determination or prediction of TBBPA 
risk to birds.
    Furthermore, EPA's use of available existing toxicity information 
reduces the use of vertebrate animals in the testing of chemical 
substances in a manner consistent with provisions described in TSCA 
section 4(h).
    2. Diet and Drinking Water Exposures. a. Diet. The petition does 
not set forth facts demonstrating that there is insufficient 
information available to EPA to reasonably determine or predict effects 
from exposure to TBBPA via diet. Testing of food products for TBBPA 
contamination, such as the plant uptake and translocation test (OCSPP 
Test Guideline 850.4800) (Ref. 31) and modified methods for TBBPA using 
the Food & Drug Administration's (FDA) Drug & Chemical Residues Methods 
(Ref. 32), requested by the petitioners, is not necessary because 
existing data are available to address this exposure pathway.
    While a plant uptake study combined with soil concentrations could 
be used to estimate dietary exposures from plants, chemicals with low 
water solubility and higher log KOW values similar to TBBPA 
are less likely to bioaccumulate in plants compared to other foods, 
such as meats, fish and dairy products (Ref. 33). Hence, other food 
items, such as meats, fish and dairy products would be expected to be 
primary contributors to dietary exposures. Available market basket 
surveys for TBBPA support this, with most samples comprised of lipid-
rich food groups (Ref. 34). There were 465 food samples collected in 
Europe between 2003 and 2010. Most of these were comprised of lipid-
rich food groups; however, some vegetable and grain based food groups 
were sampled. All samples from this study were below the level of 
quantification, which was approximately <1 ng/g wet weight, although 
this varied by food group (Ref. 35). To address dietary exposure from 
TBBPA, EPA could use a combination of approaches. First, there are 
existing plant uptake studies available that could be used to estimate 
TBBPA concentrations in plants from modeled or measured near-facility 
soil concentrations (Refs. 36 and 37). These studies are not cited in 
the petition. This approach is supported by a study, that EPA 
identified since the Problem Formulation and Initial Assessment 
document was published, that compared a wide variety of plant uptake 
studies with available models that estimate soil to plant uptake (Ref. 
38). Any modeled estimate can be compared to available measured data 
and a range of values informed by both approaches could be derived. EPA 
could model soil concentrations from TRI data; these concentrations 
along with available physical-chemical properties can be used to 
reasonably estimate plant concentrations and associated dietary 
exposures. There is also an existing study that quantified soil and 
plant TBBPA concentrations near a facility (Ref. 39). This data can be 
used to supplement and/or evaluate the modeling approach. Because 
existing approaches exist for estimating plant concentrations of TBBPA 
(modeling and market basket data), the plant uptake and translocation 
test (Ref. 31) is not necessary.
    EPA recognizes that dietary exposures come from a wide variety of 
sources, not just plants. Market basket surveys provide food 
concentrations, which can be used to estimate dietary exposure. There 
are market basket surveys from other countries that measured TBBPA in 
various food products (Refs. 40 to 42). Other studies are available 
that provide data on TBBPA concentrations in breast milk or edible fish 
(Refs. 43 to 48). Fish concentrations can also be estimated from 
combining modeled or measured surface water concentrations with 
bioaccumulation/bioconcentration factors (BAF/BCF). Ingestion from 
other dietary sources, in addition to fish, shellfish, and breast milk 
(dairy, meat, fruits and vegetables and grains), can be estimated 
individually and in total using existing data. It is expected that 
ingestion of foods with higher lipid content, such as fish and milk, 
will contribute more to dietary exposure (Ref. 49) than other foods, 
such as plants. Levels may vary based on proximity to point sources 
when compared to levels detected in market basket surveys, and this can 
be considered in developing exposure scenarios and/or background 
estimates.

[[Page 14176]]

    b. Drinking Water. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict effects from exposure to TBBPA via 
drinking water. Sampling of waters in the vicinity of representative 
manufacturing and processing facilities known to discharge TBBPA, 
requested by the petitioners, is not necessary because an existing 
approach is available to address this exposure pathway.
    EPA can use release data collected under EPA's TRI program to 
characterize TBBPA concentrations in surface water near TBBPA 
manufacturing and processing facilities.
    In addition, while there are no data on TBBPA concentrations in 
finished drinking water, EPA can use surface water monitoring data as a 
surrogate for finished drinking water to assess potential risks posed 
by drinking TBBPA-contaminated water. EPA's Office of Water routinely 
derives Ambient Water Quality Criteria for the Protection of Human 
Health (Ref. 50) using the assumption that people may ingest surface 
water as a drinking water source over a lifetime. There are existing 
data on TBBPA concentrations in surface water to conduct a drinking 
water exposure assessment using surface water as a surrogate (Refs. 51 
to 53).
    EPA believes these approaches are adequate, and likely 
conservative, to assess potential exposures to drinking water. First, 
the physical-chemical and fate properties of TBBPA, such as high 
sorption, low water solubility, and high KOC indicate that 
concentrations of TBBPA in drinking water would be expected to be low 
prior to treatment. When sediment monitoring data is used with 
assumptions about KOC, organic content, and density of water 
and sediment, surface water concentrations can be estimated to be 
generally low, below the highest levels reported in surface water 
(Refs. 54 to 56). This is supported by existing surface water 
monitoring data indicating the highest concentration of TBBPA in 
surface water is 4.87 ug/L with most data below 1 ug/L (Refs. 57 and 
58). These same chemical and fate properties would indicate that 
drinking water treatment processes would further reduce TBBPA 
concentrations in finished drinking water. Overall, the contribution to 
exposure to TBBPA via drinking water is expected to be minimal.
    3. Exposure from Manufacturing and Processing. a. Communities. The 
petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict exposure to TBBPA to communities near manufacturing and 
processing facilities. Air sampling, using methods, such as EPA Air 
Method Toxic Organics-9A (TO-9A, Determination Of Polychlorinated, 
Polybrominated And Brominated/Chlorinated Dibenzo-p-Dioxins And 
Dibenzofurans In Ambient Air) (Ref. 60), sampling of soils, and 
sampling of waters in the vicinity of representative manufacturing and 
processing facilities known to discharge TBBPA, as requested by the 
petitioners, is not necessary because EPA could use an alternative 
approach to evaluate exposure to TBBPA to communities near 
manufacturing and processing facilities. EPA could use release data 
collected under EPA's TRI program and a Gaussian dispersion model, such 
as AERMOD, to quantify air concentrations and air deposition to soil, 
to water bodies and to sediments near manufacturing and processing 
facilities. AERMOD is an EPA model that has been extensively reviewed 
and validated based on comparisons with monitoring data (Ref. 60). 
Variability and uncertainty associated with variable emission rates and 
degradation over time can also be characterized using modeling 
approaches whereas one-time or limited sampling cannot provide temporal 
characterizations. In addition, EPA can use monitoring data from other 
countries as surrogate ``near-facility'' monitoring data along with 
modeled estimates. However, the petition does not address this 
possibility, let alone explain why a testing order under section 4 
would be necessary on this point. There are several references with 
sampling locations near facilities that can be considered, many of 
which were cited in the Problem Formulation and Initial Assessment 
document (Ref. 2). EPA considers this approach to be reasonable to 
determine exposure to communities near manufacturing or processing 
facilities, but may decide to pursue targeted sampling in the future 
near manufacturing and processing facilities to reduce uncertainty.
    b. Workers. The petition does not set forth facts demonstrating 
that there is insufficient information available to EPA to reasonably 
determine or predict exposure to TBBPA to workers in manufacturing and 
processing facilities.
    Since publication of the Problem Formulation and Initial Assessment 
document, EPA identified exposure monitoring data for Europe, China and 
the United States for several industries (the manufacture of epoxy 
resins and laminates; manufacture of printed circuit boards; and 
compounding of acrylonitrile butadiene styrene (ABS) resin) (Refs. 61 
to 66).
    As discussed previously, EPA is actively developing or evolving 
approaches for implementing the new provisions in amended TSCA. One 
such approach is to perform systematic literature reviews to identify 
and/or develop additional available data and modeling approaches for 
estimating worker inhalation exposure. EPA may also assess exposure 
concentration in the case of conversion of compounded ABS resin to 
finished products based on available monitoring data for other 
industries, such as manufacture of epoxy resins and laminates and 
manufacture of printed circuit boards. Furthermore, the National 
Institute of Occupational Safety and Health (NIOSH) has initiated a 
study titled: ``Assessment of Occupational Exposure to Flame 
Retardants'' that aims to quantify, characterize occupational exposure 
(inhalation, ingestion, or dermal) among workers, and to compare 
workers' exposures to those of the general population (Ref. 67). Data 
generated from the NIOSH study is expected to inform occupational 
exposures and will be considered in an occupational assessment of 
TBBPA. However, the petition fails to explain how it considered these 
points or why a testing order under section 4 would be necessary for 
additional information.
    EPA considers the approach considered in the previous paragraph to 
be reasonable to determine exposure to workers in manufacturing and 
processing facilities, but may decide to pursue targeted sampling in 
the future near manufacturing and processing facilities to supplement 
or refine these approaches.
    Dust. EPA believes the approaches described earlier in this unit 
are sufficient to characterize exposures to workers at manufacturing or 
processing facilities from external doses/concentrations. Sampling of 
settled dust (surface wipe and bulk sampling) using the OSHA Technical 
Manual (Ref. 68), as specifically requested by the petitioners, is not 
needed. Presence of TBBPA in settled dust may indicate additional 
dermal and ingestion exposures are possible. However, surface wipe 
sampling does not provide a direct estimate of dermal or ingestion 
exposure. Surface wipe sampling would need to be combined with 
information on transfer efficiency between the surface, hands, and 
objects, as well as the number of events to estimate exposures from 
ingestion (Ref. 69). EPA notes that in the NIOSH study that is in 
progress surface wipe sampling is not included, which provides support 
for

[[Page 14177]]

the conclusion that settled dust is not a customary measure for 
occupational exposure. EPA would, however, use any information 
generated from the NIOSH study considered relevant for this exposure 
pathway.
    Biomonitoring. EPA believes the approaches described previously are 
sufficient to characterize exposures to workers at manufacturing or 
processing facilities from external doses/concentrations. Therefore, 
the biomonitoring data collected following the protocols of the current 
NIOSH study, as requested by the petitioners, is not needed. EPA would, 
however, consider any data or information generated from the NIOSH 
study deemed to be relevant and applicable for discerning exposures 
from any/all exposure routes.
    4. Exposure from recycling. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict communities specifically located at 
or near and workers in facilities that recycle TBBPA-containing 
products. In the Problem Formulation and Initial Assessment document 
(Ref. 2), EPA identified three monitoring studies that describe 
concentrations of TBBPA in soil, sediment, and sludge near 
manufacturing and recycling facilities (Refs. 71, 72, 76). Since 
publication of the Problem Formulation and Initial Assessment document 
(Ref. 2), EPA has identified four monitoring studies that describe 
concentrations of TBBPA in soil, sediment, indoor and outdoor dust from 
sampling locations in and near e-waste recycling facilities in other 
countries (Refs. 70, 73 to 75). These data may be useful for estimating 
exposures at or near U.S. recycling facilities.
    However, EPA intends to further assess how comparable the nature 
and magnitude of these types of facilities and handling of TBBPA-
containing products are to facilities within the U.S. EPA may collect 
available information related to estimating potential extent and 
magnitude of exposure. For example, the following could inform 
development of exposure scenarios for recycling facilities within the 
United States:
    a. The number and location of recycling facilities in the United 
States,
    b. the types and volumes of products that are accepted by these 
sites, and
    c. the recycling and disposal methods employed at these facilities.
    With such data or information, the recycling processes used in the 
U.S. could be compared with the processes used in the studies 
characterizing the foreign facilities. However, the petition does not 
address this possibility, let alone explain why a testing order under 
section 4 would be necessary on this point. If the processes are 
similar, EPA could extrapolate from foreign facilities to U.S. 
facilities. If EPA determines these previously indicated approaches are 
not reasonable to determine exposures, then sampling of soils, 
sediments and waters in the vicinity of facilities and air to which 
workers may be exposed at facilities known to recycle TBBPA-containing 
products, as requested by the petitioners, may become necessary. EPA 
also notes that the NIOSH study, ``Assessment of Occupational Exposure 
to Flame Retardants,'' (Ref. 67) may inform occupational exposures from 
recycling facilities and will be considered in an occupational 
assessment of TBBPA. EPA also notes that the settled dust sampling and 
biomonitoring data, as requested by the petitioners, may not be the 
most appropriate data to collect for the reasons provided previously in 
Unit IV.C.3.b., but that EPA would consider any data or information 
generated from the NIOSH study deemed to be relevant and applicable for 
discerning exposures from any/all exposure routes.
    5. Exposure from disposal. a. Landfills, wastewater treatment 
plants, and sewage sludge. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict movement of TBBPA from landfills in 
soil columns. Leaching studies (OCSPP Testing Guideline 835.1240) (Ref. 
77), requested by the petitioners, are not necessary because an 
existing approach is available to address this fate pathway. Studies 
measuring the sorption of TBBPA to soil, sand columns, and sediment are 
available as discussed in Appendix C of the Problem Formulation and 
Initial Assessment document (Ref. 2). Larsen et al. (2001) reported 
negligible leaching potential of TBBPA applied to soil and sand 
columns. (Ref. 78). The adsorption of TBBPA to sediment has been 
reported (Ref. 79) and suggest low mobility in soil and partitioning to 
sediments. Data from these existing studies can also serve as input to 
soil transport models to estimate mobility.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict transformation processes of TBBPA, which would be episodically 
and/or continuously released to wastewater. The simulation tests to 
assess the primary and ultimate biodegradability of chemicals 
discharged to wastewater (OPPTS Test Guideline 835.3280) (Ref. 80), 
requested by the petitioners, is not needed because primary degradation 
and major transformation products can be determined from existing 
studies on the ultimate biodegradability of TBBPA in aerobic and 
anaerobic sludge. One of the studies (Ref. 81) was discussed in 
Appendix C of EPA's Problem Formulation and Initial Assessment (Ref. 
2). Two additional studies (Refs. 82 and 83) were identified after 
publication of EPA's document (Ref. 2). Li, et al. (2015) (Ref. 82) 
studied TBBPA transformation in nitrifying activated sludge (NAS). 
TBBPA transformation was accompanied by mineralization. Twelve 
metabolites, including those with single benzene ring, O-methyl TBBPA 
ether, and nitro compounds, were identified during the study. Potvin et 
al. (2012) (Ref. 83) measured the removal of TBBPA from influent to 
conventional activated sludge, submerged membrane and membrane aerated 
biofilm reactors. Removal of TBBPA from these wastewater treatment 
systems was found to be due to a combination of adsorption and 
biological degradation. Nyholm, et al. 2010 (Ref. 81) reported 
transformation as biodegradation half-lives for TBPPA in aerobic 
activated sludge, aerobic digested sludge, and anaerobic activated 
sludge amended soils.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict effects from dietary exposure to crops where TBBPA contaminated 
sewage sludge is applied. A plant uptake and translocation test (OCSPP 
Test Guideline 850.4800) (Ref. 31), requested by the petitioners, is 
not necessary because existing data are available to address this fate 
pathway. As explained in the dietary exposure section, there are 
existing plant uptake studies available (Refs. 36 and 37). These data 
are also available to be used to estimate plant concentrations of 
agricultural crops where TBBPA-containing sewage sludge is applied. 
While a plant uptake study combined with sewage sludge concentrations 
could be used to estimate dietary exposures from plants, chemicals with 
low water solubility and higher log KOW values similar to 
TBBPA, are less likely to bioaccumulate in plants compared to other 
foods, such as meats, fish and dairy products (Ref. 33). Hence, other 
food items, such as meats, fish and dairy products, would be expected 
to be primary contributors to dietary exposures. Available market 
basket surveys for TBBPA support this, with most samples comprised of 
lipid-

[[Page 14178]]

rich food groups (Ref. 34). To address dietary exposure from TBBPA, EPA 
could use a combination of approaches as described in the dietary 
exposure section. EPA believes this approach can provide a reasonable 
estimate of plant concentrations of agricultural crops grown where 
TBBPA-containing sewage sludge was applied.
    b. Incineration. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict communities specifically located 
near facilities that incinerate TBBPA or TBBPA-containing products.
    Electronic waste can be sent to waste-to-energy incinerators (Ref. 
84). EPA's Problem Formulation and Initial Assessment for TBBPA (Ref. 
2) included a study that measured TBBPA emissions (0.008 ng/L to air) 
from a mixed household and commercial waste incinerator in Japan (Ref. 
85). These data may be useful for estimating exposures at or near U.S. 
facilities that incinerate TBBPA or TBBPA-containing products.
    EPA intends to further assess these facilities and could use an 
approach that combines existing data to estimate the amount of 
combustion products at incineration facilities that could have formed 
from incinerating products that contain TBBPA. Such an approach could 
combine information on:
    i. The types of by-products using data from EU (2006) (Ref. 62) and 
U.S. EPA (Ref. 87);
    ii. information regarding types of consumer waste that contains 
TBBPA and may be sent to incinerators;
    iii. information on the concentrations of TBBPA in various types of 
consumer waste; some of these data are available (Refs. 86 to 91);
    iv. Toxics Release Inventory data on emissions of the dioxin, furan 
and polycyclic aromatic hydrocarbons (PAH) by-products from 
incinerators.
    The emissions of dioxins, furans and PAHs could then be modeled 
using EPA's AERMOD air dispersion model (Ref. 60) and the amount of 
these by-products that might be attributed to TBBPA could be 
determined.
    Another approach that EPA could take is to estimate exposures near 
facilities by grouping all near-facility data for a variety of 
facilities (manufacturing, processing, e-waste, disposal) to estimate a 
generic ``near-facility'' exposure. By estimating exposure in this 
manner, EPA could take advantage of the larger number of monitoring 
studies or modeled estimates.
    However, EPA intends to further assess how comparable locations 
around incineration sites would be to those around manufacturing, 
processing, e-waste, and other disposal facilities. There are factors 
that may either increase and decrease emissions and potential 
concentrations around these facilities. For example, elevated 
temperatures are likely to eliminate some amount of possible TBBPA and 
its combustion products which could reduce overall exposures. The waste 
stream and content of TBBPA in materials as part of this waste stream 
are likely to be highly variable and could result in emissions that are 
higher or lower than those in manufacturing and processing facilities. 
Comparison of facility specific information could inform which 
categories of incineration may be sufficiently different from 
manufacturing and processing facilities to potentially warrant 
environmental sampling.
    Therefore, to complement the existing data, EPA could collect 
available information related to estimating potential extent and 
magnitude of exposure (for example, the number and location of 
incineration facilities in the U.S. and the types and volumes of 
products that are accepted by these sites). Waste disposal by 
incineration as used in the United States could be then compared with 
the processes used in the studies assessing the foreign facilities. 
However, the petition does not address this possibility, let alone 
explain why a testing order under section 4 would be necessary on this 
point. If the processes are similar, EPA could extrapolate from foreign 
facilities to U.S. facilities. If EPA determines these previously 
indicated approaches are not reasonable to determine exposures, then 
sampling of soils, sediments and waters in the vicinity of facilities 
and air to which workers may be exposed at facilities known to 
incinerate TBBPA or TBBPA-containing products, as requested by the 
petitioners, may be necessary, but could be more strategic and better 
targeted when based on deliberate evaluation of available existing data 
and information.
    6. Exposure to degradation by-products. a. Degradation in water or 
soil. The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict degradation of TBBPA in water by direct photolysis. Studies 
identifying photodegradation products of TBBPA formed by direct 
photolysis in water under laboratory conditions (Ref. 92) were 
identified after the Problem Formulation and Initial Assessment 
document was published. Therefore, the photodegradation in water test 
(OCSPP Test Guideline 835.2240) (Ref. 93), requested by the 
petitioners, is not needed.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict reactions resulting from chemical or electronic excitation 
transfer from light-absorbing humic species rather than from direct 
sunlight for TBBPA. A study identifying indirect photodegradation 
products of TBBPA formed by indirect photolysis in water under 
laboratory conditions (Ref. 94) was identified after the Problem 
Formulation and Initial Assessment document was published. Therefore, 
the indirect photolysis in water test (OCSPP 835.5270) (Ref. 95), 
requested by the petitioners, is not needed.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict degradation of TBBPA in soil by photolysis. Photolysis of TBBPA 
deposited on soil or applied to soil with sludge is a possible fate 
pathway, which could involve different pathways and mechanisms other 
than photolysis in water. Existing aqueous photolysis studies and/or 
predictive models can be used to reasonably predict the degradation 
products of TBBPA. Environmental transport and exposure modeling could 
be conducted using available measured or estimated physical-chemical 
properties to estimate exposure of degradation products. This approach 
has been used by others (Ref. 96) to estimate PBT properties for 
degradation products. Therefore, the photodegradation in soil test 
(OCSPP Test Guideline 835.2410) (Ref. 97), requested by the 
petitioners, is not needed.
    b. Microbial degradation. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict microbial degradation of TBBPA in 
soil in aerobic and anaerobic conditions. EPA has identified existing 
studies/data describing aerobic and anaerobic biodegradation pathways 
of TBBPA in both soil samples potentially pre-exposed and not pre-
exposed to TBBPA. Some studies are discussed in Appendix C of EPA's 
Problem Formulation and Initial Assessment document (Refs. 81, 98 and 
99). EPA identified two additional studies after publication of the 
Problem Formulation and Initial Assessment document that also address 
this endpoint (Refs. 82 and 100). These studies allow EPA to reasonably 
determine transformation products and

[[Page 14179]]

predict relative rates from aerobic and anaerobic microbial degradation 
in soil. Therefore, the aerobic and anaerobic transformation in soil 
test (OECD Test Guideline 307) (Ref. 101) and terrestrial soil-core 
microcosm test (OCSPP Test Guideline 850.4900) (Ref. 102), requested by 
the petitioner, are not needed.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict aerobic aquatic biodegradation of TBBPA. Studies are available 
(Refs. 103 and 104) to reasonably determine aerobic aquatic 
biodegradation pathways and products as discussed in Appendix C of 
EPA's Problem Formulation and Initial Assessment document (Ref. 2). 
Therefore, the aerobic mineralization in surface water-simulation 
biodegradation test (OCSPP Test Guideline 835.3190) (Ref. 105), 
requested by the petitioner, is not needed.
    As noted in the exposure from disposal discussion, the petition 
does not set forth facts demonstrating that there is insufficient 
information available to EPA to reasonably determine or predict 
degradation processes of TBBPA, which would be episodically and/or 
continuously released to wastewater. The simulation tests to assess the 
primary and ultimate biodegradability of chemicals discharged to 
wastewater (OPPTS Test Guideline 835.3280) (Ref. 80), which the 
petitioner cited in the discussion about exposure to degradation by-
products, is not needed.
    c. Combustion products. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict potential combustion products of 
TBBPA. The reference to combustion testing cited by the petitioners and 
others is available (Refs. 62 and 106). However, knowledge of the types 
and volumes of TBBPA-containing products is needed to use this data to 
estimate potential exposures to combustion products. As stated in the 
Problem Formulation and Initial Assessment document (Ref. 2; page 91), 
``. . . contribution of TBBPA to combustion byproducts is not possible 
to determine.'' However, EPA could acquire this information from 
recycling and incineration facilities using approaches described in 
Units IV.C.4. and IV.C.5.b. The petition does not address this 
possibility, let alone explain why a testing order under section 4 
would be necessary on this point.
    d. Toxicity of degradation products. The petition does not set 
forth facts demonstrating that there is insufficient information 
available to EPA to reasonably determine or predict characterization of 
TBBPA degradation products, and, as stated in Units IV.C.5.a, IV.C.6.a, 
and IV.C.6.b., EPA has an understanding of the products potentially 
formed from TBBPA degradation (e.g., tri-, di-, and monobromobisphenol 
A, bisphenol A, TBBPA--bis(methyl ether), isopropyl dibromophenols). 
EPA can use predictive models (e.g., EPA's EPISuite models (Ref. 107) 
to estimate the key physical-chemical properties of these degradants. 
EPISuite models have been validated and peer reviewed, and TBBPA 
degradates are chemicals for which EPISuite models are suitable for 
estimating (i.e., are within applicability domains of EPISuite models). 
EPISuite has been used for estimating chemical properties in risk 
assessments conducted by the USEPA, the EU, and Canada. Therefore, the 
use of the EPA series 830 Group B testing guidelines (Ref. 108), 
requested by the petitioners, is not needed.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict toxicity effects of TBBPA degradation products to mammals and 
birds. The petition did not reflect a comprehensive search and review 
for existing toxicity data on potential degradation products, and EPA's 
Problem Formulation and Initial Assessment document (Ref. 2) did not 
purport to represent such a comprehensive search for degradation 
products. To address the need for mammal or avian toxicity under EPA's 
current approach, EPA would conduct a comprehensive literature review 
to identify existing data for these chemicals or for analogs. Following 
identification and review of existing data, if EPA deemed specific 
testing necessary to fill identified data gaps, EPA would consider 
testing according to EPA series 850 Ecological Effects Test Guidelines 
(Ref. 109), EPA series 870 Health Effects Test Guidelines (Ref. 110), 
or appropriate OECD Guidelines.
    The petition does not set forth facts demonstrating that there is 
insufficient information available to EPA to reasonably determine or 
predict the toxicity effects of TBBPA degradation products to aquatic 
organisms. The petition did not reflect a comprehensive search and 
review for existing toxicity data on potential degradation products, 
and EPA's Problem Formulation and Initial Assessment document (Ref. 2) 
did not purport to represent such a comprehensive search. To address 
the need for aquatic toxicity under EPA's current approach, EPA would 
conduct a comprehensive literature review to identify existing data for 
these chemicals or for analogs. EPA also believes there are alternative 
approaches available to EPA regarding ecological effects of TBBPA 
degradation products on aquatic organisms. EPA could use EPA's ECOSAR 
(Ref. 111) to estimate the aquatic toxicity of these degradants. ECOSAR 
is an expert system and collection of models (i.e., Quantitative 
Structure Activity Relationships) that estimate toxicity from structure 
and physical-chemical properties of a chemical. The models incorporated 
into ECOSAR have been validated and peer reviewed. ECOSAR models are 
suitable for estimating toxicity of potential TBBPA degradates (i.e., 
TBBPA degradation product chemicals are within the applicability 
domains of ECOSAR models). Therefore, the use of the EPA series 850 
testing guidelines (Ref. 109), requested by the petitioners, is not 
needed for aquatic organisms.
    Furthermore, EPA's use of available existing toxicity information 
and modeling approaches reduces the use of vertebrate animals in the 
testing of chemical substances in a manner consistent with provisions 
described in TSCA section 4(h).
    7. Hazard endpoints. a. Reproductive toxicity, developmental 
toxicity and neurotoxicity. The petition does not set forth facts 
demonstrating that there is insufficient information available to EPA 
to reasonably determine or predict reproductive, developmental and 
neurotoxicity of TBBPA. Therefore, the reproductive/developmental 
toxicity screening test (OECD Test Guideline 421) (Ref. 112), NTP's 
Modified One-Generation Reproduction Study (Ref. 113) and the 
complementing Developmental Neurotoxicity Study (OECD Test Guideline 
426) (Ref. 114), requested by the petitioners, are not necessary. EPA 
has identified 15 reproductive/developmental toxicity tests conducted 
by the oral route of which some include evaluation of neurotoxicity 
endpoints. The available studies include: A one-generation reproduction 
toxicity test (Refs. 115 and 9); two 2-generation reproduction tests 
(Refs. 116 to 118); four prenatal developmental toxicity tests, 
including a developmental neurotoxicity test (Refs. 119 to 122); and 
six postnatal developmental toxicity tests, with some that also include 
a prenatal component (Refs. 123 to 128). All of these studies, except 
Hass et al. (2003) (Ref. 119) and Kim et al. (2015) (Ref. 126), were 
described in Appendix G of the published Problem Formulation and 
Initial Assessment document for TBBPA

[[Page 14180]]

(Ref. 2). These studies are either equivalent or superior to the 
methods used in the reproductive/developmental toxicity screening test 
(OECD Test Guideline 421) (Ref. 112) and the NTP Modified One-
Generation Reproduction Study (Ref. 113).
    For developmental neurotoxicity, a study for this endpoint by the 
oral route is available (Ref. 119), and EPA would consider the results 
of this study when evaluating risks from TBBPA. Although the study was 
conducted when the Developmental Neurotoxicity Study OECD Test 
Guideline 426 (Ref. 114) was a draft guideline, the study is adequate 
for consideration as part of a weight-of-evidence analysis along with 
the results of a 2-generation reproduction toxicity study that included 
a neurotoxicity component (Ref. 121).
    Furthermore, EPA conducted an in-depth review of the existing 
dataset of reproductive and developmental toxicity studies identified, 
as well as additional animal and human data that evaluated 
neurotoxicity endpoints (Refs. 131 and 116) following the publication 
of the Problem Formulation and Initial Assessment document (Ref. 2) and 
determined that the developmental, reproductive and neurotoxicity 
endpoints are adequately addressed. Therefore, EPA could use this body 
of existing data in selecting studies for use in risk evaluation.
    Furthermore, EPA's use of available existing toxicity information 
reduces the use of vertebrate animals in the testing of chemical 
substances in a manner consistent with provisions described in TSCA 
section 4(h).
    b. Amphibian endocrine system. The petition does not set forth 
facts demonstrating that there is insufficient information available to 
EPA to reasonably determine or predict adverse endocrine-related 
effects from exposure to TBBPA. Therefore, the larval amphibian growth 
and development assay (LAGDA) (OCSPP Test Guideline 890.2300) (Ref. 
132) is not necessary. Data are available that address thyroid effects 
of TBBPA for both bioactivity and dose response (Refs. 57 and 133 to 
139). These data include mixed results in amphibians and more 
consistent results in mammals indicating that changes in thyroid 
hormones are associated with developmental effects (specifically 
neurobehavioral effects). Given the weight-of-evidence, EPA does not 
believe that the LAGDA would significantly change this conclusion. 
Furthermore, EPA's use of this available existing toxicity information 
reduces the use of vertebrate animals in the testing of chemical 
substances in a manner consistent with provisions described in TSCA 
section 4(h).
    8. EPA's conclusions. EPA denied the request to issue an order 
under TSCA section 4 because the TSCA section 21 petition does not set 
forth sufficient facts for EPA to find that the information currently 
available to the Agency, including existing studies (identified prior 
to or after publication of EPA's Problem Formulation and Initial 
Assessment) on TBBPA and analogs, as well as alternate approaches for 
risk evaluation, is insufficient to permit a reasoned determination or 
prediction of the health or environmental effects of TBBPA at issue in 
the petition nor that the specific testing the petition identified is 
necessary to develop additional information, as elaborated throughout 
Unit IV of this notice.
    Furthermore, to the extent the petitioners request vertebrate 
testing, EPA emphasizes that future petitions should discuss why such 
testing is appropriate, considering the reduction of testing on 
vertebrates encouraged by section 4(h) of TSCA, as amended.

V. References

    The following is a listing of the documents that are specifically 
referenced in this document. The docket includes these documents and 
other information considered by EPA, including documents that are 
referenced within the documents that are included in the docket, even 
if the referenced document is not physically located in the docket. For 
assistance in locating these other documents, please consult the 
technical person listed under FOR FURTHER INFORMATION CONTACT.

1. Earthjustice, Natural Resources Defense Council, Toxic-Free 
Future, Safer Chemicals, Healthy Families, BlueGreen Alliance, 
Environmental Health Strategy Center; Eve Gartner, Earthjustice; and 
Veena Singla, Natural Resources Defense Council to Gina McCarthy, 
Administrator, Environmental Protection Agency. Re: Petition to 
Order Testing of Tetrabromobisphenol A (CAS No. 79-94-7) under 
Section 4(a) of the Toxic Substances Control Act. December 13, 2016.
2. EPA. TSCA Work Plan Chemical Problem Formulation and Initial 
Assessment Tetrabromobisphenol A and Related Chemicals Cluster Flame 
Retardants. 2015.
3. World Health Organization International Agency for Research on 
Cancer. IARC Monographs on the Evaluation of Carcinogenic Risks to 
Humans. 2014. (retrieved on February 4, 2017) https://monographs.iarc.fr/ENG/Publications/internrep/14-002.pdf.
4. Hamers, T. et al. In Vitro Profiling of the Endocrine-Disrupting 
Potency of Brominated Flame Retardants. Toxicological Sciences. 
92:157. 2006.
5. Shi, H. et al. Teratogenic effects of tetrabromobisphenol A on 
Xenopus tropicalis embryos. Comp. Biochemistry & Physiology Part C: 
Toxicology & Pharmacology. 152:62[hyphen]68. 2010.
6. Zatecka, E. et al. Effect of tetrabrombisphenol A on induction of 
apoptosis in the testes and changes in expression of selected 
testicular genes in CD1 mice. Reproductive Toxicology. 35:32 2013.
7. Meerts, I. et al. In vitro estrogenicity of polybrominated 
diphenyl ethers, hydroxylated PDBEs, and polybrominated bisphenol A 
compounds. Environmental Health Perspective. 2001.
8. Pullen, S. et al. The flame retardants tetrabromobisphenol A and 
tetrabromobisphenol A/bisallylether suppress the induction of 
interleukin-2 receptor a chain (CD25) in murine splenocytes. 
Toxicology. 2003.
9. Van der Ven, L. et al. Endocrine effects of tetrabromobisphenol-A 
(TBBPA) in Wistar rats as tested in a one-generation reproduction 
study and a subacute toxicity study. Toxicology. 2008.
10. EPA. Persistent Bioaccumulative Toxic (PBT) Chemicals; Lowering 
of Reporting Thresholds for Certain PBT Chemicals; Addition of 
Certain PBT Chemicals; Community Right-to-Know Toxic Chemical 
Reporting; Final Rule. Federal Register. (Oct. 29, 1999, 64 FR 
58666) (FRL-6389-11).
11. EPA. Response to Petition to Order Testing of 
Tetrabromobisphenol A (CAS No. 79-94-7) Under Section 4(a) of the 
Toxic Substances Control Act. 2017.
12. EPA. Assessments for TSCA Work Plan Chemicals. https://www.epa.gov/assessing-and-managing-chemicals-under-tsca/assessments-tsca-work-plan-chemicals (retrieved on February 21, 2017).
13. EPA. Work Plan Chemical Problem Formulation and Initial 
Assessment and Data Needs Assessment Documents for Flame Retardant 
Clusters. 2015. https://www.epa.gov/assessing-and-managing-chemicals-under-tsca/tsca-work-plan-chemical-problem-formulation-and-2.
14. EPA. Procedures for Chemical Risk Evaluation under the Amended 
Toxic Substances Control Act; Proposed Rule. Federal Register (82 FR 
7565, January 19, 2017) (FRL-9957-75). https://www.regulations.gov/document?D=EPA-HQ-OPPT-2016-0654-0001.
15. EPA. Procedures for Prioritization of Chemicals for Risk 
Evaluation under Toxic Substances Control Act; Proposed Rule. 
Federal Register (82 FR 4826, January 17, 2017) (FRL-9957-74). 
https://www.regulations.gov/document?D=EPA-HQ-OPPT-2016-0636-0001.
16. EPA. Docket EPA-HQ-OPPT-2016-0654. 2016.https://www.regulations.gov/document?D=EPA-HQ-OPPT-2016-0654-0001.
17. OECD. Test No 417: Toxicokinetics. Guideline for the testing of 
chemicals.

[[Page 14181]]

OECD Guidelines for the Testing of Chemicals, Section 4: Health 
Effects. OECD Publishing, Paris. 2010.
18. OECD. Test No. 427: Skin Absorption: In Vivo Method. OECD 
Guidelines for the Testing of Chemicals, Section 4: Health Effects. 
OECD Publishing, Paris. 2004.
19. Knudsen, G.A., J.M. Sanders, A.M. Sadik, and L.S. Birnbaum. 
Disposition and kinetics of tetrabromobisphenol A in female Wistar 
Han rats. Toxicology reports. 1, 214-223.2014.
20. Yu et al. Absorption and excretion of tetrabromobisphenol A in 
male Wistar rats following subchronic dermal exposure. Chemosphere. 
146:189-194. 2016.
21. Klassen, C.D. Editor: Cassarett and Doull's Toxicology: The 
Basic Science of Poisons. Seventh Edition. McGraw-Hill Medical 
Publishing Division. New York. 2008.
22. Abdallah, M. A-E., Tilston, E., Harrad, S. and C. Collins. In 
vitro assessment of the bioaccessibility of brominated flame 
retardants in indoor dust using a colon extended model of the human 
gastrointestinal tract. Journal of Environmental Monitoring. 
14:3276-3283. 2012.
23. IRDC (International Research and Development Corporation). 1975. 
Fourteen-Day Inhalation Toxicity Study in Rats (Unpublished). (as 
cited in EC, 2006).
24. EPA. Early Seedling Growth Toxicity. OCSPP Test Guideline 
850.4230. 1998.
25. ACC-BFRIP (American Chemistry Council Brominated Flame Retardant 
Industry Panel). Tetrabromobisphenol A: A Toxicity Test to Determine 
the Effects of the Test Substance on Seedling Emergence of Six 
Species of Plants. Study conducted by Wildlife International Ltd., 
March 5. Project No 439-102. 2002.
26. EPA. Acute Inhalation Toxicity (OCSPP Test Guideline 870.1300). 
1998.
27. Halldin, K., C. Berg, A. Bergman, I. Brandt, and B. Brunstrom. 
Distribution of Bisphenol a and Tetrabromobisphenol a in Quail Eggs, 
Embryos and Laying Birds and Studies on Reproduction Variables in 
Adults Following in Ovo Exposure. Archives of Toxicology. 75, 597-
603. 2001.
28. Berg, C., K. Halldin, and B. Brunstrom. Effects of Bisphenol a 
and Tetrabromobisphenol a on Sex Organ Development in Quail and 
Chicken Embryos. Environmental Toxicology and Chemistry. 20(12), 
2836-2840. 2001.
29. Hudson, R.H., et al. Handbook of toxicity of pesticides to 
wildlife. Resource Publication. Washington, DC (1984).
30. Driver, C.J., Drown, D.B., Ligotke, M.W., Van Voris, P., 
McVeety, B.D. and Greenspan, B.J. Routes of uptake and their 
relative contribution to the toxicologic response of Northern 
bobwhite (Colinus virginianus) to an organophosphate pesticide. 
Environmental Toxicology and Chemistry. 10: 21-33. 1991.
31. EPA. Plant Uptake and Translocation (OCSPP Test Guideline 
850.4800). 1998.
32. FDA. DIOXINS: FDA Strategy for Monitoring, Method Development, 
and Reducing Human Exposure. 2002, Feb. 7. Retrieved from http://www.fda.gov/Food/FoodborneIllnessContaminants/ChemicalContaminants/ucm077432.htm.
33. She, Ya-Zhe, et al. ``Bioaccumulation of polybrominated diphenyl 
ethers and several alternative halogenated flame retardants in a 
small herbivorous food chain.'' Environmental pollution 174 (2013): 
164-170.
34. Shi, Z.X., Wu, Y.N., Li, J.G., Zhao, Y.F., & Feng, J.F. (2009). 
Dietary exposure assessment of Chinese adults and nursing infants to 
tetrabromobisphenol-A and hexabromocyclododecanes: occurrence 
measurements in foods and human milk. Environmental science & 
technology, 43(12), 4314-4319.
35. EFSA 2011: Scientific Opinion on TBBPA and its derivatives in 
Food. EFSA Panel on Contaminants in the Food Chain.
36. Li, Y., Q. Zhou, Y. Wang, and X. Xie. Fate of 
Tetrabromobisphenol a and Hexabromocyclododecane Brominated Flame 
Retardants in Soil and Uptake by Plants. Chemosphere. 82(2), 204-
209. 2011.
37. Suominen, K., Verta, M., and Marttinen, S. Hazardous organic 
compounds in biogas plant end products--Soil burden and risk to food 
safety. Science of the Total Environment. 491:192-199. 2014.
38. Takaki K, Wade AJ, Collins CD. Assessment of plant uptake models 
used in exposure assessment tools for soils contaminated with 
organic pollutants. Environmental Science and Technology. 
48(20):12073-82. 2014.
39. Wang, J., L. Liu, J. Wang, B. Pan, X. Fu, G. Zhang, L. Zhang, 
and K. Lin. Distribution of Metals and Brominated Flame Retardants 
(BFRs) in Sediments, Soils and Plants from an Informal E-Waste 
Dismantling Site, South China. Environmental Science Pollution 
Research International. 22(2), 1020-1033. 2015.
40. de Winter-Sorkina, R., Bakker, M.I., Van Donkersgoed, G., and 
Van Klaveren, J.D. Dietary intake of brominated flame retardants by 
the Dutch population. RIVM report 31305001/2003. RIVM--Netherlands 
Institute of Public Health and the Environment. 2003.
41. Murata, S., Nakagawa, R., Ashizuka, Y., Hori, T., Yasutake, D., 
Tobiishi, K., and Sasaki, K. Brominated flame retardants (HBCD, 
TBBPA and [Sigma]PBDEs) in market basket food samples of Northern 
Kyushu district in Japan. Organohalogen Compounds. 69:1985-1988. 
(2007).
42. Nakao, T., Kakutani, H., Akiyama, E., and Ohta, S. Levels of 
tetrabromobisphenol A and its related compounds in infant foods in 
Japan. Organohalogen Compounds. 75:169-172. 2013.
43. Luigi, V., M. Giuseppe, and R. Claudio. Emerging and priority 
contaminants with endocrine active potentials in sediments and fish 
from the river Po (Italy). Environmental Science and Pollution 
Research. 22(18):14050-14066. 2015.
44. He, M.-J., X.-J. Luo, L.-H. Yu, J.-P. Wu, S.-J. Chen, and B.-X. 
Mai. Diasteroisomer and Enantiomer-Specific Profiles of 
Hexabromocyclododecane and Tetrabromobisphenol a in an Aquatic 
Environment in a Highly Industrialized Area, South China: Vertical 
Profile, Phase Partition, and Bioaccumulation. Environmental 
Pollution. 179:105-110. 2013.
45. Ohta, S., T. Okumura, H. Nishimura, T. Nakao, A. Osamau, and H. 
Miyata. Characterization of Japanese Pollution by PBDEs, TBBPA, 
PCDDs/DFs, PBDDs/DFs and PXDDs/DFs Observed in the Long-Term Stock- 
Fishes and Sediments. Abstracts of the 3rd International Workshop on 
Brominated Flame Retardants. 2004.
46. Harrad, S., and Abdallah, M. A.-E. Concentrations of 
Polybrominated Diphenyl Ethers, Hexabromocyclododecanes and 
Tetrabromobisphenol-A in Breast Milk from United Kingdom Women Do 
Not Decrease Over Twelve Months of Lactation. Environmental Science 
and Technology. 49(23):13899-13903. 2015.
47. Lankova, D., O. Lacina, J. Pulkrabova, and J. Hajslova. The 
determination of perfluoroalkyl substances, brominated flame 
retardants and their metabolites in human breast milk and infant 
formula. Talanta. 117:318-325. 2013.
48. Shi, Z., Y. Jiao, Y. Hu, Z. Sun, X. Zhou, J. Feng, J. Li, and Y. 
Wu. Levels of tetrabromobisphenol A, hexabromocyclododecanes and 
polybrominated diphenyl ethers in human milk from the general 
population in Beijing, China. Science of the Total Environment. 
452:10-18. 2013.
49. Shi, Z., Zhang, L., Li, J., Zhao, Y., Sun, Z., Zhou, X., and Wu, 
Y. Novel brominated flame retardants in food composites and human 
milk from the Chinese Total Diet Study in 2011: Concentrations and a 
dietary exposure assessment. Environment International. 96:82-90. 
2016.
50. U.S. EPA (OW). Methodology for Deriving Ambient Water Quality 
Criteria for the Protection of Human Health. October. EPA-822-B-00-
004.2000.
51. Quade, S.C. 2003. Determination of Tetrabromobisphenol a in 
Sediment and Sludge. (M.Sc.), University of Guelph, Guelph, Ontario.
52. Xiong, J., T. An, C. Zhang, and G. Li. 2015. Pollution Profiles 
and Risk Assessment of Pbdes and Phenolic Brominated Flame 
Retardants in Water Environments within a Typical Electronic Waste 
Dismantling Region. Environ Geochem Health, 37(3), 457-473.
53. Yang, S., S. Wang, H. Liu, and Z. Yan. 2012. Tetrabromobisphenol 
A: Tissue Distribution in Fish, and Seasonal Variation in Water and 
Sediment of Lake Chaohu, China. Environmental Science and Pollution 
Research, 19(9), 4090-4096.
54. ECHA 2016. Guidance on information requirements and chemical 
safety assessment. Chapter R.16: Environmental exposure assessment.
55. Guerra, P., E. Eljarrat, and D. Barcelo. 2010. Simultaneous 
Determination of

[[Page 14182]]

Hexabromocyclododecane, Tetrabromobisphenol a, and Related Compounds 
in Sewage Sludge and Sediment Samples from Ebro River Basin (Spain). 
Analytical and Bioanalytical Chemistry, 397, 2817-2824.
56. Zhang, X.L., X.J. Luo, S.J. Chen, J.P. Wu, and B.X. Mai. 2009. 
Spatial Distribution and Vertical Profile of Polybrominated Diphenyl 
Ethers, Tetrabromobisphenol a, and Decabromodiphenylethane in River 
Sediment from an Industrialized Region of South China. Environ 
Pollut, 157(6), 1917-1923.
57. Yang, S., Z. Yan, F. Xu, S. Wang, and F. Wu. Development of 
freshwater aquatic life criteria for tetrabromobisphenol A in China. 
Environmental Pollution. 169:59-63. 2012.
58. Harrad, S., M.A. Abdallah, N.L. Rose, S.D. Turner, and T.A. 
Davidson. Current-Use Brominated Flame Retardants in Water, 
Sediment, and Fish from English Lakes. Environmental Science and 
Technology. 43(24), 9077-9083. 2009.
59. EPA. Office of Research and Development. Compendium Method TO-
9A: Determination Of Polychlorinated, Polybrominated And Brominated/
Chlorinated Dibenzo-p-Dioxins And Dibenzofurans In Ambient Air. 
1999. https://www3.epa.gov/ttnamti1/files/ambient/airtox/to-9arr.pdf.
60. EPA. AERMOD. Technology Transfer Network Support Center for 
Regulatory Atmospheric Modeling, Meteorological Processors and 
Accessory Programs. Air dispersion software. 2016. https://www3.epa.gov/ttn/scram/dispersion_prefrec.htm#aermod.
61. ACC. 2000. Brominated Flame Retardant End-User Survey--Phase 1. 
Study conducted by Breysse, P., and J. Kacergis, Johns Hopkins 
School of Hygiene and Public Health. Baltimore, MD. Doc ID 
84010000001. May 19, 2000.
62. EC (European Commission). European Union Risk Assessment Report 
for 2,2',6,6'-Tetrabromo-4,4'-Isopropylidenediphenol 
(Tetrabromobispheonl-A or TBBP-A) Part II--Human Health, CAS No. 79-
94-7, EINECS No. 201-236-9. 4th Priority List, Volume: 63, EUR22161 
EN. Institute for Health and Consumer Protection, Joint Research 
Centre, Luxembourg. 2006. http://esis.jrc.ec.europa.eu/doc/risk_assessment/REPORT/tbbpaHHreport402.pdf.
63. M[auml]kinen, M.S.E., M[auml]kinen, M.R.A., Koistinen, J.T.B., 
Pasanen, A., Pertti, O.P., Kalliokoski, P.J., and Korpi, A.M. 
Respiratory and Dermal Exposure to Organophosphorus Flame Retardants 
and Tetrabromobisphenol A at Five Work Environments. Environmental 
Science and Technology. 43 (3), pp 941-947. 2009.
64. Rosenberg, C., M. Hameila, J. Tornaeus, K. Sakkinen, K. 
Puttonen, A. Korpi, M. Kiilunen, M. Linnainmaa, and A. Hesso. 2011. 
Exposure to Flame Retardants in Electronics Recycling Sites. Ann 
Occup Hyg, 55(6), 658-665.
65. Thuresson K, Bergman A, Jakobsson K. Occupational exposure to 
commercial decabromodiphenyl ether in workers manufacturing or 
handling flame-retarded rubber. Environmental Science and 
Technology. 39:1980-1986. 2005.
66. Zhou, X., J. Guo, W. Zhang, P. Zhou, J. Deng, and K. Lin. 2014. 
Tetrabromobisphenol A Contamination and Emission in Printed Circuit 
Board Production and Implications for Human Exposure. J Hazard 
Mater, 273(2014), 27-35.
67. NIOSH. Assessment of Occupational Exposure to Flame Retardants. 
2014. https://ntp.niehs.nih.gov/ntp/about_ntp/bsc/2014/dec/nioshupdate_508.pdf.
68. OSHA. OSHA Technical Manual (OTM), OSHA Instruction TED 01-00-
015 [TED 1-0.15A]. https://www.osha.gov/dts/osta/otm/otm_ii/otm_ii_2.html.
69. Gorman Ng, M., Semple, S., Cherrie, J.W., Christopher, Y., 
Northage, C., Tielemans, C., Veroughstraete, V. and M. Van Tongeren. 
2012. The Relationship Between Inadvertent Ingestion and Dermal 
Exposure Pathways: A New Integrated Conceptual Model and a Database 
of Dermal and Oral Transfer Efficiencies. Annals of Occupational 
Hygiene. 56(9):1000-1012.
70. Matsukami, H., N.M. Tue, G. Suzuki, M. Someya, H. Tuyen le, P.H. 
Viet, S. Takahashi, S. Tanabe, and H. Takigami. Flame retardant 
emission from e-waste recycling operation in northern Vietnam: 
Environmental occurrence of emerging organophosphorus esters used as 
alternatives for PBDEs. Science of The Total Environment. 514, 492-
499. 2015.
71. Qu, G., A. Liu, T. Wang, C. Zhang, J. Fu, M. Yu, J. Sun, N. Zhu, 
Z. Li, G. Wei, Y. Du, J. Shi, S. Liu, and G. Jiang. Identification 
of tetrabromobisphenol A allyl ether and tetrabromobisphenol A 2,3-
dibromopropyl ether in the ambient environment near a manufacturing 
site and in mollusks at a coastal region. Environmental Science and 
Technology. 47(9), 4760-4767. 2013.
72. Schlabach, M., M. Remberger, E. Brorstrom-Lunden, K. Norstrom, 
L. Kaj, H. Andersson, D. Herzke, A. Borgen, and M. Harju. Brominated 
Flame Retardants (BFR) in the Nordic Environment. TemaNord. 
2011:528. Nordic Council of Ministers, Copenhagen, Denmark. 2011. 
http://www.norden.org/en/publications/publikationer/2011-528.
73. Wang, J., Liu, L., Wang, J., Pan, B., Fu, X., Zhang, G., . . . 
and Lin, K. Distribution of metals and brominated flame retardants 
(BFRs) in sediments, soils and plants from an informal e-waste 
dismantling site, South China. Environmental Science and Pollution 
Research. 22(2):1020-1033. 2015.
74. Wang, W., K.O. Abualnaja, A.G. Asimakopoulos, A. Covaci, B. 
Gevao, B. Johnson-Restrepo, T. A. Kumosani, G. Malarvannan, T.B. 
Minh, H.-B. Moon, H. Nakata, R.K. Sinha, and K. Kannan. A 
comparative assessment of human exposure to tetrabromobisphenol A 
and eight bisphenols including bisphenol A via indoor dust ingestion 
in twelve countries. Environment International. 83, 183-191. 2015.
75. Wu, Y, et al. Tetrabromobisphenol A and heavy metal exposure via 
dust ingestion in an e-waste recycling region in southeast China. 
Science of the Total Environment. 541: 356-364. 2016.
76. Xu, T., J. Wang, S.-z. Liu, C. Lu, W.L. Shelver, Q. X. Li, and 
J. Li. A highly sensitive and selective immunoassay for the 
detection of tetrabromobisphenol A in soil and sediment. Analytica 
Chimica Acta. 751, 119-127. 2012.
77. EPA. Leaching studies (OCSPP Test Guideline 835.1240). 2008.
78. Larsen, G., F. Casey, A. Bergman, and H. Hakk. Mobility, 
Sorption and Fate of Tetrabromobisphenol a (TBBPA) in Loam Soil and 
Sand. Abstracts of the 2nd International Workshop on Brominated 
Flame Retardants. Part 2--Analysis and Fate, Products, Standards and 
Uses. Stockholm, Sweden. 2001. https://www.researchgate.net/profile/Tom_Harner/publication/244465065_Measurements_of_OctanolAir_Partition_Coefficients_(_K_OA_)_
for_Polybrominated_Diphenyl_Ethers_(PBDEs)_Predicting_Partitioning_in
_the_Environment/file/9c960526a70f0039a2.pdf.
79. GLCC (Great Lakes Chemical Corporation). The Subchronic Toxicity 
of Sediment-Sorbed Tetrabromobisphenol a to Chironomus tentans under 
Flow-through Conditions (Final Report) with Cover Sheet and Letter 
Dated 101689. Study conducted by Breteler, R.J., J.R. Hoberg, N. 
Garvey, S.R. Connor, D.A. Hartley, S.P. Shepherd, P.H. Fackler, and 
P.D. Royal, Springborn Laboratories, Inc., Wareham, MA. OTS# 
0525507. Doc ID 40-8998109. 1989.
80. EPA. Simulation tests to assess the primary and ultimate 
biodegradability of chemicals discharged to wastewater (OPPTS Test 
Guideline 835.3280). 2008.
81. Nyholm, J.R., C. Lundberg, and P.L. Andersson. Biodegradation 
kinetics of selected brominated flame retardants in aerobic and 
anaerobic soil. Environmental Pollution. 158(6):2235-2240. 2010.
82. Li, F., J. Wang, B. Jiang, X. Yang, P. Nastold, B. Kolvenbach, 
L. Wang, Y. Ma, P.F. Corvini, and R. Ji. Fate of tetrabromobisphenol 
A (TBBPA) and formation of ester- and ether-linked bound residues in 
an oxic sandy soil. Environmental Science and Technology. 
49(21):12758-12765. 2015.
83. Potvin, C.M., Z. Long, and H. Zhou. Removal of 
tetrabromobisphenol a by conventional activated sludge, submerged 
membrane and membrane aerated biofilm reactors. Chemosphere. 
89(10):1183-1188. 2012.
84. EPA. Electronics Waste Management in the United States through 
2009. EPA 530-R-11-002. Office of Resource Conservation and 
Recovery, Washington, DC. 2011. http://www.epa.gov/osw/conserve/materials/ecycling/docs/fullbaselinereport2011.pdf.
85. Borgnes, D., and B. Rikheim. Decomposition of BFRs and Emission 
of Dioxins from Co-Incineration of MSW and Electrical and Electronic 
Plastics

[[Page 14183]]

Waste. Organohalogen Compounds. 66, 890-898. 2004.
86. Gallen, C., A. Banks, S. Brandsma, C. Baduel, P. Thai, G. 
Eaglesham, A. Heffernan, P. Leonards, P. Bainton, and J.F. Mueller. 
2014. Towards Development of a Rapid and Effective Non-Destructive 
Testing Strategy to Identify Brominated Flame Retardants in the 
Plastics of Consumer Products. Sci Total Environ, 491-492, 255-265.
87. Guo, Q., Z. Du, Y. Zhang, X. Lu, J. Wang, and W. Yu. 2013. 
Simultaneous Determination of Bisphenol a, Tetrabromobisphenol a, 
and Perfluorooctanoic Acid in Small Household Electronics Appliances 
of ``Prohibition on Certain Hazardous Substances in Consumer 
Products'' Instruction Using Ultra-Performance Liquid 
Chromatography-Tandem Mass Spectrometry with Accelerated Solvent 
Extraction. J Sep Sci, 36(4), 677-683.
88. Puype, F., J. Samsonek, J. Knoop, M. Egelkraut-Holtus, and M. 
Ortlieb. 2015. Evidence of Waste Electrical and Electronic Equipment 
(Weee) Relevant Substances in Polymeric Food-Contact Articles Sold 
on the European Market. Food Addit Contam Part A Chem Anal Control 
Expo Risk Assess, 32(3), 410-426.
89. Rani, M., W.J. Shim, G.M. Han, M. Jang, Y.K. Song, and S.H. 
Hong. 2014. Hexabromocyclododecane in Polystyrene Based Consumer 
Products: An Evidence of Unregulated Use. Chemosphere, 110, 111-119.
90. Samsonek, J., and F. Puype. 2013. Occurrence of Brominated Flame 
Retardants in Black Thermo Cups and Selected Kitchen Utensils 
Purchased on the European Market. Food Addit Contam Part A Chem Anal 
Control Expo Risk Assess, 30(11), 1976-1986.
91. Washington State DE (Department of Ecology). 2016. Children's 
Safe Product Act Reports. https://fortress.wa.gov/ecy/cspareporting/Reports/ReportViewer.aspx?ReportName=ChemicalReportByCASNumber.
92. Wang, X., X. Hu, H. Zhang, F. Chang, and Y. Luo. Photolysis 
kinetics, mechanisms, and pathways of tetrabromobisphenol A in water 
under simulated solar light irradiation. Environmental Science and 
Technology. 49(11):6683-6690. 2015.
93. EPA. Photodegradation in water test (OCSPP Test Guideline 
835.2240). 2008.
94. Bao, Y., and J. Niu. Photochemical transformation of 
tetrabromobisphenol A under simulated sunlight irradiation: 
Kinetics, mechanism and influencing factors. Chemosphere. 134:550-
556. 2015.
95. EPA. Indirect photolysis in water test (OCSPP Test Guideline 
835.5270). 2008.
96. EC (European Commission). Risk Assessment of 2,2',6,6-
Tetrabromo-4,4'-Isopropylidene Diphenol (Tetrabromobisphenol-A): CAS 
Number: 79-94-7; EINECS Number: 201-236-9; Final Environmental Risk 
Assessment Report of February 2008. R402_0802_env. Rapporteur: 
United Kingdom. 2008. http://echa.europa.eu/documents/10162/17c7379e-f47b-4a76-aa43-060da5830c07.
97. EPA. Photodegradation in soil test (OCSPP Test Guideline 
835.2410). 2008.
98. GLCC (Great Lakes Chemical Corporation). 1989. Determination of 
the Biodegradability of Tetrabromobisphenol A in Soil under Aerobic 
Conditions. Final Report. Study conducted by, Springborn Life 
Sciences, Inc., (January 20, 1989), Wareham, MA. OTS# 0525513. Doc 
ID 42083 G3-2.
99. GLCC (Great Lakes Chemical Corporation). 1989. Determination of 
the Biodegradability of Tetrabromobisphenol A in Soil under 
Anaerobic Conditions (Final Report) with Attachments and Cover 
Letter Dated 013189. Study conducted by, Springborn Life Sciences, 
Inc., (January 19, 1989), Wareham, MA. OTS# 0525513. Doc ID 42083 
G3-2.
100. Liu, J., Y. Wang, B. Jiang, L. Wang, J. Chen, H. Guo, and R. 
Ji. Degradation, metabolism, and bound-residue formation and release 
of tetrabromobisphenol A in soil during sequential anoxic-oxic 
incubation. Environmental Science and Technology. 47(15):8348-8354. 
2013.
101. EPA. Aerobic and anaerobic transformation in soil test (OECD 
Test Guideline 307). 2008.
102. EPA. Terrestrial soil-core microcosm test (OCSPP Test Guideline 
850.4900). 2008.
103. NITE (National Institute of Technology and Evaluation). #32: 
Bioaccumulation: Aquatic/Sediment for TBBPA (CASRN 79-94-7). Japan 
Chemicals Collaborative Knowledge Database, Ministry of Economy, 
Trade and Industry and Ministry of the Environment, Japan. 2010. 
http://www.safe.nite.go.jp/jcheck/template.action?ano=849andmno=4-0205andcno=79-94-7andrequest_locale=en (retrieved on November 14, 
2014).
104. Fackler, P. Tetrabromobisphenol A. Determination of 
Biodegradability in a Sediment/Water Microbial System. SLS Report 
89-8-3070. Springborn Life Sciences, Inc., Wareham, MA. 1989. http://www.epa.gov/chemrtk/pubs/summaries/phenolis/c13460rr3.pdf. 
(retrieved in 2006).
105. EPA. Aerobic mineralization in surface water-simulation 
biodegradation test (OCSPP Test Guideline 835.3190). 2008.
106. EPA. Flame Retardants in Printed Circuit Boards: Final Report. 
EPA Publication 744-R-15-001. Design for the Environment (now Safer 
Choice), Washington, DC. 2015. https://www.epa.gov/sites/production/files/2015-08/documents/pcb_final_report.pdf. (retrieved in 2017).
107. EPA. Episuite (Estimation Programs Interface). 2000-2012. 
https://www.epa.gov/tsca-screening-tools/epi-suitetm-estimation-program-interface (retrieved in 2017).
108. EPA (n.d.). Series 830--Product Properties Test Guidelines. 
https://www.epa.gov/testguidelines-pesticides-and-toxic-substances/series-830-product-properties-test-guidelines (retrieved in 2016).
109. EPA (n.d.). Series 850--Ecological Effects Test Guidelines. 
https://www.epa.gov/test-guidelines-pesticides-and-toxic-substances/series-850-ecological-effects-test-guidelines (retrieved in 2016).
110. EPA (n.d.). Series 870--Health Effects Test Guidelines. https://www.epa.gov/test-guidelines-pesticides-and-toxic-substances/series-870-health-effects-test-guidelines (retrieved in 2016).
111. EPA. ECOSAR v1.11. 2012. https://www.epa.gov/tsca-screening-tools/ecological-structure-activity-relationships-ecosar-predictive-model (retrieved in 2017).
112. OECD Test No. 421: Reproductive/Developmental Toxicity 
Screening Test. OECD Guidelines for the Testing of Chemicals, 
Section 4: Health Effects. OECD Publishing, Paris. 2007.
113. NTP (National Toxicology Program) (n.d.). Modified One-
Generation Studies.https://ntp.niehs.nih.gov/testing/types/mog/index.html (retrieved in 2016).
114. OECD Test No. 426: Developmental Neurotoxicity Study. OECD 
Guidelines for the Testing of Chemicals, Section 4: Health Effects. 
OECD Publishing, Paris. 2007.
115. Lilienthal, H., C.M. Verwer, L.T. van der Ven, A. H. Piersma, 
and J.G. Vos. Exposure to Tetrabromobisphenol a (TBBPA) in Wistar 
Rats: Neurobehavioral Effects in Offspring from a One-Generation 
Reproduction Study. Toxicology. 246(1), 45-54. 2008.
116. MPI Research. An Oral Two Generation Reproductive, Fertility 
and Developmental Neurobehavioral Study of Tetrabromobisphenol-A in 
Rats (Unpublished). 2002.
117. MPI Research. Amendment to the Final Report. An Oral Two 
Generation Reproductive, Fertility and Developmental 
Neurobehavioural Study of Tetrabromobisphenol-A in Rats (Unpublished 
Report). 2003.
118. Zatecka, E., L. Ded, F. Elzeinova, A. Kubatova, A. Dorosh, H. 
Margaryan, P. Dostalova, and J. Peknicova. Effect of 
tetrabromobisphenol A on induction of apoptosis in the testes and 
changes in expression of selected testicular genes in CD1 mice. 
Reproductive Toxicology. 35:32-39. 2013.
119. Hass, H., C. Wamberg, O. Ladefoged, M. Dalgaard, H. Rye Lam, 
and A. Vinggard. Developmental Neurotoxicity of Tetrabromobisphenol 
A in Rats (Unpublished; Cited in EC, 2006). 2003.
120. MPI Research. Final Report--an Oral Prenatal Developmental 
Toxicity Study with Tatrabromobisphenol-A in Rats (Unpublished). 
2001.
121. Noda, T., S. Morita, S. Ohgaki, and M. Shimizu. Safety 
Evaluation of Chemicals for Use in Household Products (VII) 
Teratological Studies on Tetrabromobisphenol-A in Rats. Annual 
Report of the Osaka Institute of Public Health and Environmental 
Sciences, 48, 106-112. 1985.
122. VCC (Velsicol Chemical Corporation). Pilot Teratology Study in 
Rats with

[[Page 14184]]

Tetrabromobisphenol A with Cover Letter Dated 04/17/78. 0200479. 
1978.
123. Eriksson, P., E. Jakobsson, and A. Fredriksson. Developmental 
Neurotoxicity of Brominated Flame Retardants, Polybrominated 
Diphenyl Ethers, and Tetrabromobisphenol A. Organohalogen Compounds, 
35, 375-377. 1998.
124. Eriksson, P., E. Jakobsson, and A. Frederiksson. Brominated 
Flame Retardants: A Novel Class of Developmental Neurotoxicants in 
Our Environment? Environmental Health Perspectives. 109, 903-908. 
2001.
125. Fukuda, N., Y. Ito, M. Yamaguchi, K. Mitumori, M. Koizumi, R. 
Hasegawa, E. Kamata, and M. Ema. Unexpected Nephrotoxicity Induced 
by Tetrabromobisphenol a in Newborn Rats. Toxicology Letters. 150, 
145-155. 2004.
126. Kim, B., E. Colon, S. Chawla, L.N. Vandenberg, and A. Suvorov. 
Endocrine disruptors alter social behaviors and indirectly influence 
social hierarchies via changes in body weight. Environmental health: 
A global access science source. 14, 64. 2015.
127. Saegusa, Y., H. Fujimoto, G.H. Woo, K. Inoue, M. Takahashi, K. 
Mitsumori, A. Nishikawa, and M. Shibatani. Developmental Toxicity of 
Brominated Flame Retardants, Tetrabromobisphenol a and 1,2,5,6,9,10-
Hexabromocyclododecane, in Rat Offspring after Maternal Exposure 
from Mid-Gestation through Lactation. Reproductive Toxicology. 28, 
456-467. 2009.
128. Saegusa, Y., H. Fujimoto, G.H. Woo, T. Ohishi, L. Wang, K. 
Mitsumori, A. Nishikawa, and M. Shibutani. Transient Aberration of 
Neuronal Development in the Hippocampal Dentate Gyrus after 
Developmental Exposure to Brominated Flame Retardants in Rats. 
Archives of Toxicology. 86(9), 1431-1442. 2012.
129. Tada, Y., T. Fujitani, N. Yano, H. Takahashi, K. Yuzawa, H. 
Ando, Y. Kubo, A. Nagasawa, A. Ogata, and H. Kamimura. Effects of 
Tetrabromobisphenol a, a Brominated Flame Retardant, in ICR Mice 
after Prenatal and Postnatal Exposure. Food and Chemical Toxicology. 
44(8), 1408-1413. 2006.
130. Viberg, H., and P. Eriksson. Differences in Neonatal 
Neurotoxicity of Brominated Flame Retardants, PBDE 99 and TBBPA, in 
Mice. Toxicology. 289(1), 59-65. 2011.
131. Kicinski, M., M.K. Viaene, E.D. Hond, G. Schoeters, A. Covaci, 
A.C. Dirtu, V. Nelen, L. Bruckers, K. Croes, I. Sioen, W. Baeyens, 
N. Van Larebeke, and T.S. Nawrot. 2012. Neurobehavioral Function and 
Low-Level Exposure to Brominated Flame Retardants in Adolescents: A 
Cross-Sectional Study. Environmental Health, 11, 1-12.
132. EPA. Larval amphibian growth and development assay (LAGDA) 
(OCSPP Test Guideline 890.2300). 2002.
133. ACC. HPV Data Summary and Test Plan for Phenol, 4,4'-
Isopropylidenbis[2,6-Dibromo- (Tetrabromobisphenol a, TBBPA). Test 
plan revision/updates, revised test plan. Robust summaries & test 
plans: Phenol, 4,4'-isopropylidenbis[2,6-dibromo-. 2006. (retrieved 
in 2013) http://www.epa.gov/chemrtk/pubs/summaries/phenolis/c13460rt3.pdf.
134. Garber, E.A.E., G.L. Larsen, H. Hakk, and A. Bergman. Frog 
Embryo Teratogenic Assay: Xenopus (FETAX) Analysis of the Biological 
Activity of Tetrabromobisphenol a (TBBPA). Poster presentation at 
Second International Workshop on Brominated Flame Retardants, May 
14-16, Stockholm University, Sweden. 2001.
135. Balch, G.C., and C.D. Metcalfe. In Vivo Toxicity Testing of 
PBDEs Using Early Life Stages of the Japanese Medaka and the Xenopus 
Tail Resorption Model. 3rd Annual Workshop on Brominated Flame 
Retardants in the Environment. Canada Centre for Inland Waters, 
August 23-24, pp. 59-60. 2001. (as cited in EC, 2006 and ACC, 2006).
136. Brown, D.D., Z. Wang, J.D. Furlow, A. Kanamori, R.A. 
Schawartzman, B.F. FRemo, and A. Pinder. The thyroid hormone-induced 
tail resorption program during Xenopus laevis metamorphosis. 
Developmental Biology. 93:1924-1929. 1996.
137. Hanada, H., K. Katsu, T. Kanno, E.F. Sato, A. Kashiwagi, J. 
Sasaki, M. Inoue, and K. Utsumi. Cyclosporin a Inhibits Thyroid 
Hormone-Induced Shortening of the Tadpole Tail through Membrane 
Permeability Transition. Comparative Biochemistry and Physiology. 
Part B, 135, 473-483. 2003.
138. Kashiwagi, A., H. Hanada, M. Yabuki, T. Kanno, R. Ishisaka, J. 
Sasaki, M. Inoue, and K. Utsumi. Thyroxine Enhancement and the Role 
of Reactive Oxygen Species in Tadpole Tail Apoptosis. Free Radical 
Biology and Medicine. 26(7/8), 1001-1009. 1999.
139. Veldhoen, N., A. Boggs, K. Walzak, and C.C. Helbing. Exosure to 
Tetrabromobisphenol-a Alters Th-Associated Gene Expression and 
Tadpole Metamorphosis in the Pacific Tree Frog Pseudacris regilla. 
Aquatic Toxicology. 78, 292-302. 2006.

List of Subjects in 40 CFR Chapter I

    Environmental protection, Flame retardants, Hazardous substances, 
tetrabromobisphenol A.

    Dated: March 10, 2017.
Wendy Cleland-Hamnett,
Acting Assistant Administrator, Office of Chemical Safety and Pollution 
Prevention.
[FR Doc. 2017-05291 Filed 3-16-17; 8:45 am]
 BILLING CODE 6560-50-P