Document ID: EPA-HQ-OPPT-2017-0414-0115
Agency: epa
Document Type: Supporting & Related Material
Title: 
Posted Date: 2018-08-17T04:00Z

United States
Environmental Protection Agency
United States
Environmental Protection Agency
Premanufacture Notification Number: P-12-0453-0433
Office of Chemical Safety and Pollution Prevention
Premanufacture Notification Number: P-12-0453-0433
Office of Chemical Safety and Pollution Prevention

                                       
                       TSCA New Chemicals Review Program
                      Standard Review Risk Assessment on
                                       
                      Medium-Chain Chlorinated Paraffins 
                                (PMN P-12-0453)
                                       
                                      and
                                       
                       Long-Chain Chlorinated Paraffins 
                                (PMN P-12-0433)
                                       

This assessment was conducted under EPA's TSCA Section 5 New Chemicals Review Program. EPA is assessing Medium-Chain Chlorinated Paraffin (MCCP) and Long-Chain Chlorinated Paraffin (LCCP) chemicals as part of its New Chemicals Review program. As with all Premanufacture Notice (PMN) submissions, EPA followed the approaches, methods and statutory provisions of TSCA section 5 for the chlorinated paraffin PMNs assessments as well as general EPA risk assessment practices (USEPA 1988, 2014). Finally, a draft of this assessment was made public to request more information and receive public comment (USEPA, 2015). 

                                  CONCLUSIONS
                                       
Based on its assessment of the available surrogate hazard and exposure information on P-12-0453 and P-12-0433, EPA/OPPT concludes the following pertaining to the manufacturing, processing and use of these PMN substances: 

1. Occupational Exposures: Given the assumptions, data and scenarios evaluated in this assessment, there were no risks found for workers from either dermal or inhalation exposures to either of the PMN substances.

2. General Population Exposures (from environmental releases): Given the assumptions, data and scenarios evaluated in this assessment, there were no risks found to humans from environmental releases via exposure to drinking water for either of the PMN substances, or from exposure via from fish ingestion (P-12-0433, the LCCP). There were three scenarios (3 out of 44) where potential risks to the general population due to fish ingestion were identified using the E-FAST modeling results. These scenarios were further evaluated using the highest measured values of MCCPs in fish. Using these measured values and high-end (95[th] percentile) fish intake assumptions, there were no risks identified. There were no risks found to humans from environmental releases via inhalation exposures from emissions from facilities for either PMN. 

3. Environmental Assessment:
a. Using the conventional EPA PMN method of estimating water concentrations, all of the intended processes and uses for P-12-0453 and 0433 are expected to result in releases to the surface water at concentrations that may present an unreasonable risk following acute and chronic exposures to aquatic organisms. Use of additional information submitted in response to comments on a previous draft did result in decreases of estimated risk values for some scenarios.

b. Using available measured concentrations of MCCP and LCCP congener groups in the environment as supporting information, the PMN substances:
            i.	Are expected to partition to sediment and may partition to soil through land application of biosolids, and
            ii.	May be released to the environment at water concentrations that may present an unreasonable risk following acute and chronic exposures to aquatic organisms.
            iii.	May be released to the environment resulting in sediment concentrations that may present an unreasonable risk following chronic exposures to sediment organisms.

4. PBT Assessment: The PMN substances may be very persistent and very bioaccumulative.

 TABLE OF CONTENTS
TABLE OF CONTENTS	3
1	INTRODUCTION	6
1.1	PMNS RECEIVED	6
1.2	CHEMISTRY	6
1.3	USES	9
2	ENVIRONMENTAL FATE	9
2.1	ENVIRONMNETAL PERSISTENCE	10
2.2	BIOCONCENTRATION AND BIOACCUMULATION	11
3	ECOLOGICAL HAZARD OVERVIEW	13
4	HUMAN HEALTH HAZARD OVERVIEW	16
4.1	MCCP HEALTH DATA REVIEW	16
4.2	LCCP HEALTH DATA REVIEW	18
5	EXPOSURE INFORMATION	19
5.1	ENVIRONMENTAL MONITORING	19
5.2	MODELED ENVIRONMENTAL RELEASES	22
5.2.1	Assessment Scope	22
5.2.1.1	P-12-0453 (MCCP)	22
5.2.1.2	P-12-0433 (LCCP)	23
5.2.2	Assessment Approach	23
5.2.3	Environmental Release Assessment	24
5.2.4	Summary of Release Assessment	26
5.2.5	Modeled Environmental Concentrations	27
5.3	OCCUPATIONAL EXPOSURE ESTIMATES	29
5.3.1	Assessment Scope	29
5.3.2	Assessment Approach	30
5.3.3	Summary of Occupational Exposure Assessment	31
5.3.4	CONSUMER EXPOSURE ESTIMATES	32
6	RISK ASSESSMENT	32
6.1	ENVIRONMENTAL ASSESSMENT	32
6.1.1	Risk Estimates Using Environmental Monitoring Concentrations	32
6.1.2	Risk Estimates Using Modeled Exposures	34
6.2	HUMAN HEALTH	37
6.2.1	Workers	37
6.2.2	General Population	40
7	CONCLUSIONS	46
8	REFERENCES	48
9	APPENDICES	62
Appendix A	ENVIRONMENTAL FATE AND BIOACCUMULATION STUDY SUMMARIES	63
A-1	ENVIRONMENTAL PERSISTENCE	63
A-1-1	Abiotic Degradation	63
A-1-1-1	Fate in Air	63
A-1-2	Biodegradation	64
A-1-2-1	Fate in Wastewater Treatment	64
A-1-2-2	Fate in Surface Water, Sediments and Groundwater	65
A-1-2-3	Fate in Soil	65
A-2	BIOCONCENTRATION AND BIOACCUMULATION	70
Appendix B	ECOTOXICITY STUDY SUMMARIES	79
B-1	MCCP ECOTOXICITY DATA	79
B-1-1	Acute Fish Toxicity	79
B-1-2	Acute Aquatic Invertebrate Toxicity	80
B-1-3	Algae Toxicity	83
B-1-4	Chronic Fish Toxicity	84
B-1-5	Chronic Aquatic Invertebrate Toxicity	87
B-1-6	Chronic Aquatic Sediment Invertebrate Toxicity	90
B-1-7	Avian Toxicity	92
B-1-8	Terrestrial Invertebrate Toxicity	93
B-1-9	Terrestrial Plant Toxicity	94
B-1-10	Conclusions	95
B-2	LCCP ECOTOXICITY DATA	96
B-2-1	Acute Fish Toxicity	96
B-2-2	Acute Aquatic Invertebrate Toxicity	97
B-2-3	Aquatic Plant Toxicity	98
B-2-4	Chronic Fish Toxicity	99
B-2-5	Chronic Aquatic Invertebrate Toxicity	99
B-2-6	Chronic Aquatic Sediment Invertebrate Toxicity	103
B-2-7	Avian Toxicity	103
B-2-8	Terrestrial Invertebrate Toxicity	103
B-2-9	Terrestrial Plant Toxicity	103
B-2-10	Conclusions	103
Appendix C	HUMAN HEALTH HAZARD STUDY SUMMARIES	105
C-1	MCCP HEALTH DATA REVIEW	105
C-1-1	Metabolism	105
C-1-2	Acute Toxicity	105
C-1-3	Irritation and Sensitization	106
C-1-4	Repeated-dose Toxicity	106
C-1-5	Genotoxicity	107
C-1-6	Carcinogenicity	107
C-1-7	Developmental Reproductive Toxicity Review	112
C-2	LCCP HEALTH DATA REVIEW	118
C-2-1	Metabolism	118
C-2-2	Acute Toxicity	118
C-2-3	Irritation and Sensitization	118
C-2-4	Repeated-dose Toxicity	119
C-2-5	Genotoxicity	119
C-2-6	Carcinogenicity	119
C-2-7	Developmental Reproductive Toxicity Review	119
Appendix D	ENVIRONMENTAL MONITORING	123
D-1	MCCP MONITORING DATA	123
D-1-1	Surface Water	123
D-1-2	Sediment	125
D-1-3	Biosolids and Soil	134
D-1-4	Biota	134
D-2	LCCP MONITORING DATA	137
Appendix E	ENGINEERING (ChemSTEER) REPORTS ON P-12-0-0433 and P-12-0453	138
Appendix F	EXPOSURE SCENARIO ESTIMATES	165
Appendix G	SUPPLEMENTAL INFORMATION	169

INTRODUCTION
PMNS RECEIVED
INEOS Chlor Americas, Inc. (hereinafter "INEOS") submitted two Premanufacture Notices (PMNs) identified by the Environmental Protection Agency/Office of Pollution Prevention and Toxics (EPA/OPPT) as either medium-chain chlorinated paraffins (MCCPs; P-12-0453) of varying chain lengths with the formula CxH(2x-y+2)Cly and "x" equaling 14 to 17 and "y" equaling 6 to > 24 or long-chain chlorinated paraffins (LCCPs; P-12-0433) of varying chain lengths with the formula of CxH(2x-y+2)Cly and "x" equaling 18 to 20 and "y" equaling 6 to > 24. Table 1 lists the basic information INEOS supplied on these two PMNs which are intended to be sold under the trade name "Cereclor[(R)]".

Table 1: Identification, Production Volume and Use of P-12-0453 and P-12-0433
                                      PMN
                                 Chemical Name
                             1[st] Year Production
                                  Volume (kg)
                            % PMN in final Product
                                     Uses
                                    Log KOW
                               Water Solubility
                                   P-12-0453
                            Alkanes, C14-17, chloro
                             (MCCPs; 40-60 wt% Cl)
                                      CBI
                                     5-20
74%: lubricant in metal working fluids (MWFs);
17%: flame retardant/plasticizer in polymers; 
7%: plasticizer in adhesives; and 
2%: lubricant in sealants.
                                   4.70 (E)
                              < 0.03 mg/L (E)
                                   P-12-0433
                            Alkanes, C18-20, chloro
              (LCCPs; 40-55 weight percent chlorination [wt% Cl])
                                      CBI
                                      15
100%: lubricant in MWFs
                                   7.46 (E)
                              < 0.006 mg/L (E)
E = Estimated

Though the specific PMNs in this application include MCCPs and LCCPs, this standard review presents data and information on short-chain chlorinated paraffins (SCCPs) and on very long-chain chlorinated paraffins (vLCCPs) analogs. The continuum of carbon chain length and degree/percent chlorination (wt% Cl) in all of the chlorinated paraffins (CPs) is important and the relationship among them needs to be kept in mind.

CHEMISTRY
Shown below are the structures and chlorine content of P-12-0453 and P-12-0433 products are shown below. 

P-12-0453: the average molecular formula ranges from C14H26Cl4 (low weight at ~40 wt% Cl) to C17H26Cl10 (high weight at ~60 wt% Cl). The parent hydrocarbon had the following measured composition: C14, 36 wt% (range 30-40 wt%); C15, 30 wt% (range 25-35 wt%); C16, 24 wt% (range 20-30 wt%); and C17, 10 wt% (8-18 wt%). 

P-12-0433: the average molecular formula ranges from C17H31Cl5 (low weight ~40 wt% Cl) to C20H34Cl8 (high weight ~50 wt% Cl). The parent hydrocarbon had the following measured composition: C17, 17.06 wt% (max 20 wt%); C18, 64.71 wt% (range 45-70 wt%); C19, 13.67 wt% (range 15-27 wt%); and C20, 2.13 wt% (range 4-12 wt%).

CPs have an unknown or variable composition (classified as UVCB compounds for TSCA Inventory purposes) of polychlorinated n-alkanes. The carbon chain length usually varies between 10 and 30 carbon atoms and the degree of chlorination can vary between 30 and 75 wt%. EPA/OPPT subdivides CPs according to their carbon chain length into the following categories:

 SCCPs (C10-13) 
 MCCPs (C14-17) 
 LCCPs (C18-20) 
 Very long-chain CPs (vLCCP, C>20)

SCCPs and MCCPs exist as liquids at standard temperature and pressure. CPs with a carbon chain length > 18 are subdivided based on their physical state, which is a function of chain length and chlorine content. The LCCPs and vLCCPs up to 70 wt% Cl are typically liquids (40  -  55 wt% Cl) while above 70 wt% Cl they are waxy solids.

CP products contain a variety of carbon chain lengths that have been chlorinated to different degrees (i.e., variation in the number and position of the chlorine atoms on the carbon chain). The individual isomer content of commercial CPs is rarely identified because the number of possible individual congener group is extremely large. Consequently, the physicochemical properties of CPs vary by carbon chain length and chlorine content. Increased molecular weight correlates to higher melting and boiling points, lower vapor pressures and water solubilities, and greater LogKOW (logarithm of octanol:water partition coefficient). EPA/OPPT used the physicochemical properties listed in Table 2 for informing its evaluation of P-12-0453 and P-12-0433. 

Table 2: Summary of Physiochemical Information[a,b]
                                       
                                    wt% Cl
                                 Melting Point
                                 Boiling Point
                                Vapor Pressure
                               Water Solubility
                                    Log KOW
MCCPs
> 40
< 25°C
(pour point)
> 200°C (dec)
< 0.036 Pa
at 20 °C
27 ug/L
at 20°C
> 5.5 (measured)
8.30 (estimated)[c][,][d]
LCCPs
> 40
< 25°C
(pour point)
> 200°C (dec)
< 2.7 x 10[-4] Pa
at 20 °C
5 ug/L 
at 20°C
> 8
[a]Source: ECB (ECB, 2008); EA (2009)
[b]Because most CP products are liquids and the CPs begin decomposing at 200 °C (via loss of HCl), melting point and boiling points are considered less important in characterizing hazard and risk.
[c]Value calculated using the KOWWIN Program (v1.68) available in EPA/OPPT's Estimation Programs Interface (EPI) Suite TM. This estimate was generated using a representative MCCP (i.e., C14H24Cl6, 52 wt% Cl) with the following SMILES notation: CCC(Cl)CC(Cl)CCCl)CC(Cl)CC(Cl)CC(Cl)C. 
[d]The ECB (ECB, 2008) cited Renberg's liquid chromatography to measure a LogKOW between 5.5 and 8.2 and then chose to use a Log KOW = 7 as a representative LogKOW for MCCPs with 45-52 wt% Cl.

Analytical challenges exist with evaluating CPs due to the sheer number of congener groups that may be present in CP products. The existence of multiple chain lengths in the UVCBs such as P-12-0453 and P-12-0433 requires the use of analytical methods that separate congener groups based on retention time in a column and mass spectrum of the respective peaks. Several lines of evidence support the use of a representative SCCP or MCCP product as a surrogate for congener groups present in MCCP or LCCP commercial products, respectively. 

Hüttig (2006) and Hüttig and Oehme (2006) reported that most commercial MCCP products were > 60 wt% of the C14 chain-length congener groups and the C15 chain-length congener  groups comprised the majority of the remaining  40 wt%. The authors found < 15 wt% C16 chain-length congener groups present in most commercial MCCP samples and little to no C17 chain-length congener groups. Additional studies have reported that the C14 and C15 chain-length congener groups are the predominant MCCPs present in environmental media and in human breast milk (Bayen et al., 2006; Chen et al., 2011; Reth et al., 2006; Wang et al., 2013). Some variation is possible in commercial products where the C14 and C15 chain-length congener groups may not be the predominant congener groups in a specific MCCP product; however, even in these products, the C14 and C15 chain-length congener groups may serve as reasonable worse case surrogates for the C16-17 chain-length congener groups, due to their greater bioavailability and mobility in environmental media (ECB, 2005). 

These analyses, in conjunction with measured or estimated physicochemical and environmental fate properties, allow for the reasonable use of associating commercial products circulating in commerce with CP levels found in environmental media and biota. For example, the experimental observation that MCCPs (C14-17) are abundant in sediment has been explained using known water solubility and vapor pressure values in conjunction with predicted degradation pathways (de Boer, 2010). Therefore, relating one commercial product with other commercial products is reasonable for attributing the hazard characterization to CPs of different sources. EPA/OPPT determined that the key studies for toxicity for both the human health and environmental organism hazard evaluations used one CP commercial product (i.e., Cereclor S52[(R)]). EPA/OPPT determined that the key studies for toxicity for both the human health and environmental organism hazard evaluations used one CP (Cereclor S52(R)) commercial product. Thus, available information (hazard and environmental monitoring data) on one commercial product (Cereclor S52(R)) is used as a representative CP for this assessment. Finally, experimental data on SCCPs show that these shorter chain products are more toxic than the longer chain CPs (e.g., MCCPs and LCCPs). Therefore, when endpoint specific data were lacking for the specific PMNs in this assessment, EPA/OPPT used measured data from SCCPs as surrogates to quantify potential hazards and risks.

USES
INEOS reported four uses for the MCCP PMN (P-12-0453), including:

1) 73.8% as a lubricant in metal working fluids (MWF) (no commercial or consumer uses). The notification substance is blended into the MWFs at 15%. 
2) 16.8% as a flame retardant/plasticizer in poly(vinyl chloride) (PVC) resins (no commercial or consumer uses). The notification substance is blended into the PVC resins at 15%. 
3) 7.4% as a plasticizer in adhesives (no commercial or consumer uses). The notification substance is blended into the adhesives at 5%. 
4) 2% as a lubricant in sealants (no commercial or consumer uses). The notification substance is blended into the sealants at 20%.

INEOS reported one category of use for the LCCP PMN (P-12-0433). This PMN substance is intended for use solely (i.e., 100% of the production volume) as a lubricant in MWF (no commercial or consumer uses). The PMN substance will be used at 15% in the final working formulation.
ENVIRONMENTAL FATE
EPA/OPPT reviewed available information on the environmental fate of MCCPs and LCCPs in different environmental compartments and the properties that control transport in the environment (summarized in Appendix A). In addition, EPA/OPPT reviewed assessments performed by Canada (EC, 2008a) and the EU (EA, 2009; ECB, 2005) to inform its assessment.

ENVIRONMNETAL PERSISTENCE
Abiotic studies have shown that MCCPs and LCCPs are stable to hydrolysis and to direct photolysis in water and air. In laboratory studies using hydrocarbon solvents, CPs were shown to poorly absorb ultraviolet (UV) light and no direct photodegradation was observed. The atmospheric half-life for MCCPs and LCCPs has been estimated at 1 - 2 days (EA, 2009; ECB, 2005), based on estimated values for the second order rate constant for reaction with atmospheric hydroxyl radicals for MCCPs (40-56 wt% Cl) and LCCPs (42-54 wt% Cl) (EA, 2009; ECB, 2005). The persistence of MCCPs increases with carbon chain length and higher chlorine content (EA, 2009; ECB, 2005). 

Existing biotic degradation data suggest there are a number of microbial species that are capable of degrading shorter chain, lower chlorinated MCCP congeners. Longer and higher chlorinated chemicals also may be degraded, but at much slower rates (Allpress and Gowland, 1999; Muir, 2010; Omori et al., 1987). The results from laboratory studies of microbial metabolism, using both isolated species and mixed cultures of acclimated microbes, show that MCCPs and LCCPs may be degraded by direct metabolism or co-metabolism by some microbes and microbial consortia in soil, wastewater treatment systems, sediment and other environmental media. Overall, the existing studies suggest that with microbial degradation, dechlorination and carbon chain cleavage may be possible in some media (see Table A-1); however, the degree of degradation is generally low (Allpress and  Gowland, 1999; Muir, 2010; Omori et al., 1987). 

In general, MCCP and LCCP congeners with longer chain lengths and higher degrees of chlorination are expected to be persistent or very persistent in some environmental compartments. In contrast, shorter and lesser-chlorinated congeners are likely to degrade rapidly, especially in aerobic environments. Because persistence increases with chain length, LCCPs are generally expected to be more persistent than MCCPs with comparable degrees of chlorination (EA, 2009; ECB, 2005). 

Based on the review of available literature and studies submitted by various manufacturers, including confidential business information (CBI) not publicly available, EPA/OPPT's conclusions regarding environmental persistence of MCCPs and LCCPs are consistent with those provided by Canada and the EU. 

The Canadian assessment on MCCPs and LCCPs states (EC, 2008a):

      "Information on physical properties of MCCPs, and especially LCCPs, is limited. Values used in this assessment are based on extrapolations mainly from SCCPs or QSARs. The analysis of SCCPs and MCCPs in sediment cores and associated calculations provide strong evidence for the persistence of these substances in the environment. Even though there are no data for persistence of LCCPs in sediment, based on biodegradation data which indicate increasing stability with increasing carbon chain length, it is reasonable to conclude that LCCPs are persistent in sediment."

The EU assessment on MCCPs states (ECB, 2005):

      "No standard ready or inherent biodegradation tests results are available for medium-chain chlorinated paraffins. From the available information, medium-chain chlorinated paraffins can be considered to be not biodegradable in such test systems and so a biodegradation rate MCCPs of 0 day-1 is used in the risk assessment. 
      
      There is evidence that some microorganisms may be capable of degrading MCCPs in the environment in acclimated or co-metabolic systems. The potential for biodegradation appears to increase with decreasing chlorine content. However, it is not possible from the available data to derive rate constants for biodegradation in soil, surface water and sediment systems. As a worst case approach, no biodegradation will be assumed in these media in the PEC calculations.
      
      Hydrolysis is not expected to be a significant degradation process for medium-chain chlorinated paraffins in the environment. An atmospheric half-life of 1-2 days is estimated for reaction with hydroxyl radicals. A value for the rate constant for the reaction (kOH) of 8 x 10[-12] cm[3] molecule[-1] s[-1] is used for the environmental modelling in the risk assessment."

The UK assessment on LCCPs concluded the following (EA, 2009):

      "Based on the laboratory studies and other data available, LCCPs are unlikely to be readily or inherently biodegradable. Although there is some evidence that they may biodegrade in the environment, it is thought likely that this process will be sufficiently slow that LCCPs meet the P or vP (very persistent) criteria."

EPA/OPPT generally concurs with these characterizations. In the absence of information on specific congener groups and data for MCCP or LCCP products, EPA/OPPT concludes that at least some congener groups present in both MCCP and LCCP products may be persistent to very persistent; with estimated half-lives in air exceeding 2 days and estimated half-lives in water, sediment and soil exceeding 2 months (60 days) (ECB, 2005; EA, 2009). These constituents include C14-17 63% Cl, C14-17 60 - 63% Cl, C14-17 51% and 53 - 56% Cl, C14 60.2% Cl and C18-20 48 - 70% Cl. Further discussion of these findings can be found in Table Apx A-2: Review of MCCP and LCCP Biodegradation Studies.

BIOCONCENTRATION AND BIOACCUMULATION
Recent reviews of the potential for MCCPs and LCCPs to bioaccumulate have shown that, while data are limited, some congener groups are bioaccumulative or very bioaccumulative (EC, 2008a; ECB, 2005; Houde et al., 2008; Thompson and Vaughan, 2014). EPA has identified constituents including C14 51% Cl and C14 63% Cl as potentially bioaccumulative or very bioaccumulative based on experimental data. Further discussion of these findings can be found in Table Apx A-3 in Appendix A.
Based on EPA/OPPT's review of existing studies (Bengtsson et al., 1979; CPC, 1980, 1983a, 1983b; Fisk et al., 1999; Fisk et al., 1998; Houde et al., 2008; Madeley and  Maddock, 1983a, 1983b; Madeley and  Thompson, 1983; Renberg et al., 1986; Thompson et al., 2000), EPA/OPPT concludes that the bioconcentration potential of MCCP and LCCP congener groups varies with the chain lengths and degree of chlorination and species evaluated. Shorter and less chlorinated chemicals are readily taken up by organisms but also may be excreted or degraded after absorption (Arnot, 2013). Longer and more highly chlorinated chemicals are typically not absorbed across cellular membranes and are not accumulated in tissues. Some MCCP chemicals with intermediate chain length and chlorination may be absorbed and retained. The available evidence for MCCP and LCCP congener groups with intermediate chain lengths and chlorination suggests that some may have bioconcentration factors (BCFs) or bioaccumulation factors (BAFs) greater than 1000 or 5000 (EC, 2008a; ECB, 2005, 2008). This suggests that some congener groups in MCCP and LCCP products may be bioaccumulative or very bioaccumulative.

The Canadian assessment on MCCPs and LCCPs states (EC, 2008a):
      
      "On the basis of the available information, and in particular the field BAF estimates, it is concluded that MCCPs are bioaccumulative substances..." 

      "On the basis of the available information, and in particular the BAF model and empirical BMF estimates, it is concluded that C18 - 20 liquid LCCPs are bioaccumulative substances..." [page 27] and "...While there is a lack of empirical bioaccumulation data for LCCPs, the modelling results provided by the Modified Gobas BAF Model - which suggest that of all the LCCPs congeners only liquid C18-20 LCCPs have significant bioaccumulation potential --  are considered credible." 

The UK assessment on LCCPs states (EA, 2009):

      "The available data for LCCPs do show that uptake into fish from food occurs in the laboratory, and that this uptake can be significant in some cases. The degree of uptake appears to be highest for the C18 - 20 liquid chlorinated paraffins, but uptake of C>20 liquid chlorinated paraffins has also been demonstrated. The uptake of the highly chlorinated C>20 solid chlorinated paraffins from food appears to be minimal."  

EPA/OPPT generally concurs with these characterizations. In the absence of information on specific congener groups and data for MCCP or LCCP products, EPA/OPPT concludes that at least some congener groups present in both MCCP and LCCP products may be bioaccumulative to very bioaccumulative based on multiple lines of evidence, including: Log KOW values, modeled BCFs, laboratory-measured BCFs, field-measured BAFs, field-measured biomagnification factors (BMFs), laboratory-measured biota-sediment accumulation factors (BSAFs) and the presence of MCCPs and LCCPs in human and wildlife biota. EPA has identified constituents including C14 51% Cl and C14 63% Cl as potentially bioaccumulative or very bioaccumulative based on experimental data. EPA has identified constituents including C14 30% Cl through C18 70% Cl as potentially bioaccumulative or very bioaccumulative based on estimated data. Further discussion of these findings can be found in Table Apx A-3: Review of MCCP and LCCP Bioaccumulation Studies and Table_Apx A-4: Estimated BCF/BAF Values for MCCP and LCCP Constituents C14-C20 30 - 70 wt % Cl 
 
ECOLOGICAL HAZARD OVERVIEW 
The available ecotoxicity data on MCCPs and LCCPs are summarized in Appendix B, along with the criteria EPA/OPPT used for identifying the highest quality studies. Ecotoxicity studies for MCCPs have been conducted in fish, aquatic invertebrates and plants, sediment and soil invertebrates, and terrestrial plants and invertebrates. Though no avian reproduction studies were available on MCCPs, a high quality study was available on an SCCP product (C10-12, 58 wt% Cl) with similar physicochemical properties to MCCPs and was used for informing EPA/OPPT's hazard evaluation (ECB, 2000). 

For LCCPs, ecotoxicity studies were only identified for aquatic invertebrates and vertebrates. No data were available on sediment-dwelling or terrestrial organisms. Overall, the available data on LCCPs were of low quality; therefore, the EPA/OPPT used data on MCCPs to inform its hazard evaluation of LCCPs. This decision was considered a reasonable worst-case scenario because although P-12-0433 contains up to 20 wt% C17, a component of MCCPs (e.g., P-12-0453) contains between 8-18 wt% C17. It is reasonable to assume that C17 congener groups have similar ecotoxicological effects when the wt. % Cl is comparable. EPA/OPPT concludes that the studies summarized in Table 3 were the highest quality for assessing potential hazards in the aquatic, sediment and terrestrial compartments. 

                                       
Table 3: Summary of Aquatic, Sediment and Terrestrial Ecotoxicity Data for MCCPs and LCCPs
                                       
                                Test Substance
                            Test Organism (Species)
                          Test Guideline; Study type
                                 End- point[1]
                                   Value[2]
                                   Reference
                             Aquatic Invertebrates
                       Cereclor S-52 (52 wt% Cl, C14-17)
                                  Water flea
                                (Daphnia magna)
OECD 202, 1984; Acute immobilization test
                                     EC50
                                    0.0059
                                  CPA (1996)
                       Cereclor S-52 (52 wt% Cl, C14-17)
                                  Water flea
                                (Daphnia magna)
OECD 202- Part II, 1984; Reproduction test
                                     NOEC
                                     LOEC
                                     MATC
                                     0.01
                                     0.018
                                     0.013
                       Thompson, Williams et al. (1997)
                        Sediment-Dwelling Invertebrates
                       Cereclor S-52 (52 wt% Cl, C14-17)
                                   Amphipod
                               (Hyalella azteca)
OECD 218- Draft, 2001; 28-day prolonged sediment toxicity study
                                     NOEC
                                     LOEC
                                     MATC
                                      130
                                      270
                                      187
                            Thompson et al. (2002)
                                       
                                       
                           Terrestrial Invertebrates
                       Cereclor S-52 (52 wt% Cl, C14-17)
                                   Earthworm
                               (Eisenia fetida)
OECD Guideline-Draft, 2000; 28-day reproductive toxicity test
                                     NOEC
                                     LOEC
                                     MATC
                                      79
                                      280
                                      149
                            Thompson et al. (2001d)
                            Terrestrial Vertebrates
                       Commercial CP (58 wt% Cl, C10-12)
                                 Mallard duck
                             (Anas platyrhynchos)
EPA 560/6-82-002; 22-week reproduction test
                                     NOEC
                                     LOEC
                                      168
                                     1000
                                  ECB (2000)
[1]EC50 = concentration that kills/immobilizes 50% of the test animals. NOEC = No observable effect concentration. LOEC = lowest observed effect concentration. MATC = Maximum acceptable toxicant concentration (geometric mean of NOEC and LOEC). 
[2]Units are mg/L for aquatic invertebrates, mg/kg dry weight sediment for sediment-dwelling invertebrates; mg/kg dry weight soil for earthworm study; and mg/kg diet for the duck study. 

Using the concentrations in the "value" column in Table 3 to represent hazard, EPA/OPPT derived concentrations of concern (COCs) by applying assessment factors of five or ten for acute or chronic exposures, respectively, which account for laboratory variability and represents species sensitivity distributions (following US EPA, 2012). The COCs derived for aquatic-, sediment- and terrestrial-dwelling organisms are explained below and summarized thereafter in Table 4. 

The most reliable and acceptable toxicity studies, with the most sensitive endpoints, to assess MCCP and LCCP toxicity to aquatic organisms for MCCPs and LCCPs, are from the CPA (1996) study for acute toxicity and the Thompson et al. (1997) study for chronic toxicity, both in daphnids. 

 Acute COC: The 48-hour EC50 value 0.0059 mg/L is divided by an assessment factor of 5 to yield an acute concentration of concern (COC) of 0.00118 mg/L, or 0.001 mg/L, or 1 μg/L (1 ppb). 
   Aquatic Acute COC = 1 ppb.
 Chronic COC: The chronic value 0.013 mg/L is divided by an assessment factor of 10 to yield 0.0013 mg/L or 1.3 μg/L or 1.3 ppb. 
   Aquatic Chronic COC = 1 ppb.
The most reliable and acceptable value to assess MCCP and LCCP acute toxicity to aquatic sediment invertebrate organisms is based the Thompson et al. (2002) 28-d study in amphipods. The 28-d sediment invertebrate GMATC value of 187 mg/kg dry wt sediment is used to assess hazard. Using methods in US EPA (2012): 

 Acute COC: The chronic value 187 mg/kg dry wt. is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,870 mg/kg dry wt. This value is then divided by an assessment factor of 5 to yield 374 mg/kg dry wt. 
   Aquatic Sediment Acute COC = 374 mg/kg dry wt sediment.
 Chronic COC: The 28-d sediment invertebrate GMATC of 187 mg/kg dry wt sediment is divided by an assessment factor of 10 to yield 18.7 mg/kg dry wt sediment. 
   Aquatic Sediment Chronic COC = 18.7 mg/kg dry wt sediment.

The most reliable and acceptable value to assess MCPP and LCCP acute toxicity to terrestrial invertebrates is from the Thompson et al. (2001d) study in earthworms. The 28-d terrestrial invertebrate GMATC value of 149 mg/kg dry wt soil from this study will be used. Using methods in US EPA (2012): 

 Acute COC: To calculate an acute concern concentration from the chronic value the value 149 mg/kg dry wt, is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,490 mg/kg dry wt. This value is then divided by an assessment factor of 5 to yield 298 mg/kg dry wt. 
   Terrestrial Invertebrate Acute COC = 298 mg/kg dry wt.
 Chronic COC: The 28-d terrestrial invertebrate GMATC of 149 mg/kg dry wt is divided by an assessment factor of 10 to yield 14.9 mg/kg dry wt. 
   Terrestrial Invertebrate Chronic COC = 14.9 mg/kg dry wt.

The most reliable and acceptable value to assess MCPP and LCCP acute toxicity to terrestrial vertebrates is based on the SCCP study in ducks reported in ECB (2000). The 22-week terrestrial vertebrate NOEC value of 168 mg/kg dry wt soil from this study will be used. Using methods in US EPA (2012): 

 Acute COC: To calculate an acute concern concentration from the chronic value the value 168 mg/kg diet is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,680 mg/kg diet. This value is then divided by an assessment factor of 5 to yield 336 mg/kg diet. 
   Terrestrial Vertebrate Acute COC = 336 mg/kg diet.
 Chronic COC: The 22-week terrestrial vertebrate NOEC of 168 mg/kg diet is divided by an assessment factor of 10 to yield 16.8 mg/kg diet. 
   Terrestrial Vertebrate Chronic COC = 16.8 mg/kg diet.

Table 4: COCs for Environmental Toxicity of MCCPs and LCCPs
                                  Compartment
                                 Test organism
                                   Endpoint
                                     Value
                               Assessment factor
                                      COC
                                 Surface water
                                  Water flea
                                     EC50
                                  5.9 ug/L 
                                       5
                                   1.2 ug/L
                                       
                                       
                                  21-day MATC
                                   13 ug/L
                                      10
                                   1.3 ug/L
                                   Sediment
                                   Amphipod
                                     MATC
                                 187 mg/kg dw
                                      10
                          18.7 mg/kg dry wt. sediment
                                  Terrestrial
                                   Earthworm
                                  28-day MATC
                                 149 mg/kg dw
                                      10
                            14.9 mg/kg dry wt. soil
                                       
                                 Mallard duck
                                 22-week NOEC
                                168 mg/kg diet
                                      10
                                16.8 mg/kg diet

HUMAN HEALTH HAZARD OVERVIEW
A summary of EPA/OPPT's evaluations on MCCPs and LCCPs is provided in sections 4.1 and 4.2, respectively; individual study reviews are provided in Appendix C.

MCCP HEALTH DATA REVIEW
Based on their low vapor pressure and low water solubility, absorption of MCCPs following inhalation or dermal exposure in humans or animals is expected to be limited. Previous evaluations concluded that absorption by the inhalation and dermal routes of exposure will not exceed 50 or 1%, respectively (ECB 2005; EA 2009). Some MCCPs demonstrated moderate absorption and metabolism following oral exposure in animals. In general, absorption and metabolism are related to the carbon chain length and degree of chlorination; the longer the carbon chain length and the higher the degree of chlorination, the less absorption and metabolism.

No information is available on the toxicity of MCCPs in humans; however, the toxicology of these compounds has been evaluated in experimental animals. Studies in rats and rabbits have shown that MCCPs caused slight skin irritation and have low eye irritation potential (referenced below and in Appendix C). No evidence of skin sensitization was found when tested in guinea pigs. The liver, kidney and thyroid are the target organs of MCCPs in oral repeated dose studies in experimental animals (see Table_Apx C-1 in Appendix C). MCCPs induced increased liver weight, enzyme activity, and histopathological changes at high dose levels. Some of these hepatic effects are likely related to an increase in metabolic demand as an adaptive response, as well as to peroxisome proliferation, which are considered of limited toxicological significant to humans. However, liver necrosis was observed in a 90-day study in rats at 360 mg/kg-bw/day; this effect is considered relevant to humans. The reported effects in the kidney may have been produced by the parent compound or from metabolites. Mechanistic data cannot totally rule out that some kidney effects are relevant to humans. From the data available, a LOAEL of 625 mg/kg-bw/day based on histopathological changes in the kidneys of female rats is identified in a 90-day toxicity study, and a NOAEL of 23 mg/kg-bw/day based on increased kidney weight at 222 mg/kg-bw/day is identified from another 90-day study in rats (CXR, 2005). Repeated dose studies in rats reported some changes in histopathology and hormone levels of the thyroid. However, it may be concluded based on an evaluation of the mechanistic data that the thyroid effects observed in rats is of little relevance to chronic toxicity in humans. This is explained more fully in Appendix C and relates to humans, unlike rodents, possessing a T4-globulin binding protein and thus less susceptible to plasma T4 depletion and hence any resultant thyroid stimulation (as seen in the rodent study).

There is no information on the carcinogenicity of MCCPs; however, carcinogenicity studies on a SCCP and a vLCCP are available. These studies, along with the genotoxicity data on MCCPs, may be used to inform the carcinogenic potential of MCCPs. When administered by gavage, a SCCP (C12, 60 wt% Cl) caused increased incidences of liver tumors in male and female rats, kidney tumors in male rats, and thyroid tumors in female rats. However, based on mechanistic considerations, these tumors are considered to be of little or no relevance to humans (details in ECB, 2008 and in Appendix C). An increased incidence of malignant lymphoma in male mice was reported at the highest dose of 5,000 mg/kg-bw/day in carcinogenicity studies of a vLCCP (C23, 43 wt% Cl) in male and female rats and mice. Because it is unlikely that MCCPs are genotoxic, and the fact that cancer was only observed at the highest dose, the EU (UK 2009) assumed that there was a threshold for this effect in the mice. In addition, there was no increased incidence of malignant lymphoma observed in the carcinogenicity study on an SCCP. Further, MCCPs are non-genotoxic. Therefore, it may be concluded that MCCPs are unlikely to pose a carcinogenic hazard to humans.
A series of range-finding and definitive prenatal developmental and reproductive toxicity studies were conducted in rats and rabbits with MCCPs. These studies were conducted between 1981 and 1986. They appear to be valid toxicity studies, conducted according to the standard methodologies available at the time.

 In several prenatal developmental toxicity studies with MCCPs conducted via gavage, no signs of maternal toxicity were seen at doses of 500 mg/kg-bw/day in rats (the LOAEL was 5,000 mg/kg-bw/day) and 100 mg/kg- bw/day in rabbits (highest dose tested). Likewise, no signs of developmental toxicity were observed at doses as high as 5,000 mg/kg-bw/day in rats and 100 mg/kg-bw/day in rabbits.

A one-generation reproductive toxicity range-finding study exposed rats to MCCP at dietary concentrations of 0, 100, 1000 or 6250 ppm in the diet (equivalent to approximately 0, 6, 62, and 384 mg/kg-bw/day in males and 0, 8, 74, or 463 mg/kg-bw/day in females) (IRDC, 1985 as cited in ECB, 2008). Results showed the following NOAELs/LOAELs: systemic toxicity  -  NOAEL of 74 mg/kg-bw/day based on a LOAEL of 463 mg/kg-bw/day for reductions in body weight gain in females; developmental toxicity  -  NOAEL of 6 or 8 mg/kg-bw/day based on a LOAEL of 62 or 74 mg/kg-bw/day for pup mortality; and reproductive toxicity  -  NOAEL of 384/463 mg/kg-bw/day (highest concentration tested). 

Additional studies with MCCPs were conducted in an effort to clarify the possible causes of the hemorrhaging in the pups (see Appendix C for more detailed review). One involved a screening cross-fostering study in rats exposed to 0 or 6,250 ppm MCCP in the diet, or 3,125 mg/kg-bw/day for four weeks (Hart et al., 1985 as cited in ECB, 2008). Results showed that pups from either control or treated animals which were reared with treated dams showed high mortality due to a disruption in a vitamin K-dependent clotting system. Another (0 or 6,250 ppm MCCP in the diet, or 538 mg/kg-bw/day for four weeks) study showed maternal death during parturition due to low levels of vitamin K and related hemorrhaging, suggesting that the act of parturition places dams at higher risk (CXR, 2004 as cited in ECB, 2008). A third study examined the possible role of clotting factors adult rats in an oral gavage study with rats receiving 0, 500 or 1000 mg/kg-bw/day MCCP for 21 days (CXR, 2003 as cited in ECB, 2008) and receiving either a normal diet or a vitamin K-deficient diet. Results showed MCCPs did not adversely affect the blood clotting system in adult females.  It was concluded from these studies that the fetus relies on clotting factors via mother's milk and severe deficiencies in vitamin K levels and related clotting factors in the pups results in hemorrhaging.

These effects in the pups were not seen in a more recent reproductive toxicity study (CXR, 2006 as cited in ECB,2008) conducted in compliance with OECD Guideline 421 (developmental/reproductive screening study); although there were a higher number of animals used and the exposure duration was longer. Rats were administered 0, 300, 600 or 1200 ppm MCCP in the diet (equivalent to 0, 21, 44 or 84 mg/kg-bw/day in males and 0, 23, 47 or 99 mg/kg-bw/day in females). Results showed the following NOAELs/LOAELs: systemic toxicity  -  NOAEL of 47 mg/kg-bw/day based on a LOAEL of 100 mg/kg-bw/day for increases in liver weight in females; developmental toxicity and reproductive toxicity  -  NOAEL of 84/99 mg/kg-bw/day (highest concentration tested). 

Internal hemorrhaging was not seen in the adult animals in the range-finding study at doses as high as 384/463 mg/kg-bw/day (6,250 ppm), or in another study in non-pregnant female rats repeatedly exposed to oral gavage doses as high as 1,000 mg/kg-bw/day. However, when dams were exposed to approximately 500 mg/kg-bw/day (6,250 ppm) MCCPs during cohabitation, gestation, and lactation, signs of hemorrhaging were observed in dams that died at the time of parturition. Taken together, the results of these studies suggest that newborns during lactation and pregnant females at the time of parturition are a potentially sensitive subpopulation; with a possible LOAEL for internal hemorrhaging and deaths in pups at an oral dose of 74 mg/kg-bw/day.

No guideline developmental neurotoxicity studies on MCCPs were located. It is not clear if any developmental neurotoxicity endpoints were measured in the available prenatal developmental/reproductive toxicity studies; none were explicitly stated. The only information available regarding behavior during development is from cage-side observations in pups through lactation day 21. In these cases, no dose-related differences were reported in F1 post-weaning appearance or cage-side behaviors. While thyroid hormone induced effects were observed in adults, no data exist for developmental studies. Current studies do not evaluate developmental neurotoxicity following perinatal exposures.

In this assessment, the lowest NOAEL (90-day value of 23 mg/kg-bw/day from the rat study described above; CXR, 2005) was used to assess occupational and non-occupational (i.e., general population) risk of MCCPs. 

LCCP HEALTH DATA REVIEW
There is no information on inhalation absorption of v/LCCPs in humans or in animals. Based on their low vapor pressure and water solubility, absorption following inhalation or dermal exposure is expected to be limited. Some absorption and metabolism following oral exposure are possible for LCCPs with shorter carbon chain length and lower degree of chlorination; and some data are reviewed in Appendix C on very long chain chlorinated paraffins (vLCCPs) showing very low absorption via the oral route (less than 1%). 

No information is available on the toxicity of LCCPs in humans. Acute oral toxicity data in animals show that v/LCCPs are of very low acute toxicity. Studies in animals have shown that some v/LCCPs may have the potential to cause slight skin irritation and sensitization but no eye irritation potential. The liver is the main target organ of v/LCCPs in repeated dose studies in experimental animals. Inflammatory and necrotic changes of the liver were observed in rats exposed to a C20-30 v/LCCP with 43 wt% Cl at dose levels of 100 mg/kg-bw and above. For another v/LCCP with C20-26 70 wt% Cl, effects in the liver occurred at a very high exposure level of 3,750 mg/kg-bw/day; the NOAEL was 900 mg/kg-bw/day. 

As noted above in Section 4.1, an increased incidence of malignant lymphoma in male mice was reported at the highest dose of 5,000 mg/kg-bw/day when tested using a C23 vLCCP with 43 wt% Cl in carcinogenicity studies in male and female rats and mice. vLCCPs are not genotoxic (see review in Appendix C, Section C-2-6), and the fact that cancer was only observed at the highest dose, the EU (UK 2009) assumed that there was a threshold for this effect in the mice. In addition, there was no increased incidence of malignant lymphoma observed in the carcinogenicity study on an SCCP (also discussed above in the MCCP section). It has been concluded that LCCPs are unlikely to pose a carcinogenic hazard to humans (NRC, 2000; Serrone et al., 1987). 
Based on the LOAEL (100 mg/kg-bw) of the liver effects in female rats of repeated dose studies,  Health Canada calculated a tolerable daily intake (TDI) of 71 μg/kg-bw/day with LCCPs. Using upper bounding intake estimates ranging from 0.007 μg/kg-bw/day for 60+ age group to 0.024 μg/kg-bw/day for 0.5 years' age group, Environment Canada determined that the exposure levels are 10,000 and 3,000 times lower, respectively, than the TDI. 

The National Research Council (NRC, 2000) reviewed the toxicological risks of selected flame retardants, including a vLCCP containing C24 with 70 wt% Cl. Based on the NOAEL of 900 mg/kg-bw/day (liver toxicity), NRC derived an RfD of 0.3 mg/kg-bw/day. Using this RfD and the worst case average daily exposure to be 0.16 mg/kg-bw/day, NRC concluded: "LCCP do not pose a noncancer risk when incorporated into residential furniture at the estimated application levels." Further, it was concluded that: "LCCP are not likely to be a human carcinogen and derivation of a cancer potency factor is unnecessary."

In this assessment, the LOAEL of 100 mg/kg-bw/day from the 90-day and two-year studies described above) was used to assess potential occupational and non-occupational (i.e., general population) risk of LCCPs. 

EXPOSURE INFORMATION
EPA/OPPT used the information in this section and our standard PMN approaches to estimate potential worker exposures from activities associated with manufacturing, processing and use of P-12-0453 and P-12-0433. Environmental releases from these activities were also estimated for use in assessing risk to both human health (general population) and the environment (aquatic organisms). In addition, EPA/OPPT reviewed the available information on measured environmental concentrations of MCCPs and LCCPs, which are not normally available for PMNs.
ENVIRONMENTAL MONITORING
For this assessment, environmental monitoring data consisting of measured levels of MCCPs and LCCPs in surface water, sediment and soil were used to characterize potential environmental exposure to MCCPs and LCCPs. These data are not amenable to determining the ultimate release source (i.e., manufacturing, processing, or use) into the environment; however, they provide some insight on the geographical and temporal distribution of MCCPs and LCCPs. Appendix D contains information and data used in this risk assessment.

Studies published between 1980 and 2013 that reported environmental concentrations of MCCPs and/or LCCPs were reviewed for this assessment. Monitoring studies from the early 1980s could not distinguish between the different chain lengths of CPs. The introduction of modern techniques, such as electron capture negative ion mass spectrometry (ECNI-MS) allowed for the detection of specific congeners, although difficulties with these methods have persisted (e.g., detection of low chlorination congeners in samples). Tomy (2010) performed a round robin laboratory study of SCCPs that highlighted the inability of the ECNI-MS method to consistently measure a reference sample, with concentrations varying up to a factor of six. Subsequent work showed that significant errors (up to a factor of ten) could be introduced by the improper selection of the calibration standards (Coelhan et al., 2000). A more recent inter-laboratory study of SCCPs found good agreement amongst the laboratories that used ECNI-MS (Pellizzato et al., 2009), but similar inter-laboratory studies for MCCPs or LCCPs have not been completed (Tomy, 2010). 

The majority of the monitoring data were collected in Europe and some more recent monitoring data were collected in China. Over time and across countries, industrial practices and effluent pre-treatment have varied. Some of the monitoring studies only published their final measured concentrations and did not include the details of the analytical techniques and sampling locations. Generally, EPA/OPPT used studies sponsored by the environmental agencies, but full documentation is lacking for even these studies. The industrial sectors studied by other countries also are present in the US, suggesting that conditions in the US may be similar. 

The level of detail provided in the studies varied. Some studies provided detailed information regarding sampling locations (e.g., impacted sites), analytical methodology and final sample results including detection limits, quantitation limits and estimated values. In contrast, other studies provided only a summary of the results combined from a number of studies. These summaries also did not provide details of the data analysis to obtain sample results. In addition, certain studies reported concentrations within a given country but did not provide additional details about the exact sampling location. Given the disparate conditions (i.e., number of sites sampled, temporal period over which samples collected, differing analytical methods, etc.) across the data sets, EPA/OPPT was unable to determine a central tendency or distribution for the data sets and a range was used instead. Studies using older analytical techniques that did not distinguish CP congeners were not used in this assessment. Other nations' assessments that used newer, more reliable, analytical techniques were considered.

EPA/OPPT used the following selection criteria to identify the studies included in this assessment:
 Specific mention of MCCP/LCCP chain length;
 Use of modern analytical techniques to distinguish categories of CPs; and
 At a minimum, general information on sampling location.

EPA/OPPT used the monitoring data summarized in Tables 5 and 6 for this assessment. When a limit of detection (LOD) value was reported for non-detectable results, EPA/OPPT used one-half of the LOD value. 

Even though the existing monitoring data were limited in quality and quantity and it remains unclear how well the measured data describe the potential range of US MCCP and LCCP use scenarios, EPA/OPPT concluded that the data in Tables 5 and 6 represented the best available monitoring information for MCCPs and LCCPs, respectively. These data provide some evidence that MCCPs and LCCPs are released into the environment; however, these data reflect discrete locations and times and the extent to which they are representative of the overall distribution of MCCPs and LCCPs is unknown.

Table 5: Summary of Measured Concentrations of MCCPs in Environmental Media and Biota.
                                Media Category
                                       n
                                      Min
                                     Unit
                                      Max
                                     Unit
                                  References
                          Surface water (non-marine)
                                      15
                              <2.50 x 10[-10]
                                     mg/L
                                1.49 x 10[-3] 
                                     mg/L
Coelhan (2010); EC (2008b); Houde et al. (2008); IPCS (1996); Muir et al. (2003); Petersen et al. (2006)[a]; USEPA (1988) 
                                   Sediment 
                                 (non-marine)
                                      78
                                2.00 x 10[-3] 
                                   mg/kg[b]
                                6.51 x 10[1] 
                                   mg/kg dw
Borgen et al. (2003); Chen et al. (2011); EC (2008a); Iozza et al. (2008); IPCS (1996); Nicholls et al. (2001); Petersen et al. (2006); Pribylova et al. (2006); Tomy et al. (1998); Tomy et al. (1999); USEPA (1988) 
                               Sediment (marine)
                                      54
                                5.00 x 10[-3] 
                                   mg/kg dw
                                1.64 x 10[1] 
                                   mg/kg dw
Hüttig et al. (2004); Hüttig and Oehme (2005, 2006); Kemmlein et al. (2002); Muir et al. (2000)
                                    Sludge
                                       9
                                5.00 x 10[-5] 
                                   mg/kg[b] 
                                9.70 x 10[3] 
                                   mg/kg dw
Stevens et al. (2003); Pribylova et al. (2006)
                                     Soil
                                      12
                                2.1 x 10[-6] 
                                   mg/kg dw
                                 8.5 x 10[-2]
                                   mg/kg dw
Iozza (2010); Wang et al. (2013)
                                    Biota 
                                   (aquatic)
                                      120
                              <2.00 x 10[-7]
                                     mg/kg
                                     2.63
                                   mg/kg ww
Bennie et al. (2000); EC (1993, 2008a); Houde et al. (2008); IVL (2009); Kemmlein et al. (2002); Muir (2010); Muir et al. (2003); Muir et al. (2000); Reth et al. (2005,2006);  Tomy et al., (1999a); USEPA (1988) 
                                    Biota 
                                 (terrestrial)
                                       8
                                5.00 x 10[-3] 
                                   mg/kg ww
                                3.70 x 10[-1]
                                   mg/kg ww
Reth et al. (2006)
[a]Petersen et al. (2006) reported results for two water samples; EPA/OPPT assumed these were non-marine surface water samples.
[b]The weight type was not reported (i.e., wet, dry, or lipid weight).
Notes:
1. All values provided in the table above represent total MCCPs and not individual MCCP isomers.
2. The "n" value represents the number of media-specific MCCP monitoring data values that were compiled from various articles in the raw data table (provided in Appendix D). 
3. In some cases, the minimum values in the table are preceded by "<". This indicates that the value reported in article was reported as a non-detect. In such cases, one half of the lowest reported detection limit was compiled as the `minimum' reported monitoring data.
4. dw  -  dry weight and ww  -  wet weight.

Table 6 below summarizes the available environmental monitoring data for LCCPs. Environmental data were available for marine sediment and aquatic invertebrates. Though no data were available for other media categories (e.g., surface water, non-marine sediment, terrestrial invertebrates), limited high quality data (from Table 6) were available for MCCPs which could be used for informing concentrations of LCCPs in the environment. This decision is based on the following information: 1) P-12-0433 commercial products contain up to 20% of C17, an MCCP congener (see Section 1.2 Chemistry), 2) LCCP congener groups are expected to behave in a manner similar to MCCP congener groups with comparable wt% Cl when released to the environment and 3) MCCP and LCCP commercial products have similar uses (see Table 1) and hence may have similar releases at facilities that process and use these chemicals.  

Table 6: Summary of Measured Concentrations of LCCPs in Environmental Media and Biota.
                                Media Category
                                       n
                                      Min
                                     Units
                                      Max
                                     Units
                                  References
                               Sediment (marine)
                                       4
                                 1.02x10[-1]
                                   mg/kg dw
                                 4.31x10[-1]
                                   mg/kg dw
Kemmlein et al. (2002) 
                                Biota (aquatic)
                                       2
                                 2.80x10[-6]
                                   mg/kg lw
                                 6.90x10[-6]
                                   mg/kg lw
Kemmlein et al. (2002)
Notes:
1. All values provided in the table above represent total LCCP C18-20 and not individual LCCP isomers.
2. The "n" value represents the number of media-specific LCCP C18-20 monitoring data values that were compiled from various articles in the raw data table (provided in Appendix D).
3. dw  -  dry weight and lw  -  lipid weight.

MODELED ENVIRONMENTAL RELEASES
The engineering report which includes more detail on the environmental release assessment including estimates, calculation approaches, basis for estimates and sources used is provided in Appendix E. The following subsections describe the scope, general approach and a summary of key results of the engineering environmental release assessment for P-12-0433 and 0453.
Assessment Scope
P-12-0453 (MCCP)
According to the PMN submission for P-12-0453, the third year production volume for the PMN chemical substances is CBI. INEOS further indicated that the substances is for import only and the intended uses for the PMN substance are split among four uses: flame retardant/plasticizer in polymers, lubricant in metal working fluids (MWFs), lubricant in sealants, and plasticizer in adhesives. EPA's initial hazard review for persistence, bioaccumulation and ecotoxicity indicated the need for the engineering assessment to evaluate potential releases to all media including water, air, landfill and incineration. Based on this information, the following assessment scope was selected.
Approximate Percentage of Production Volume:
Use 1: Flame retardant/plasticizer in polymers  -  17% 
Use 2: Lubricant in metalworking fluids  -  74%
Use 3: Lubricant in sealants  -  2%
Use 4: Plasticizer in adhesives 7%

Operations Assessed:
 Formulation of Metalworking Fluids
 Use of Metalworking Fluids
 Plastics Compounding
 Converting of Compounded Plastics into Articles
 Formulation of Adhesives and Sealants
 Use of Adhesives and Sealants
Releases assessed:
 Release to water
 Release to air
 Release to landfill
 Release to incineration

P-12-0433 (LCCP)
According to the PMN submission for P-12-0433, third year production volume for the PMN chemical substances is CBI. INEOS further indicated that the substance is for import only and the only intended uses for the PMN substance is as a lubricant in metal working fluids (MWFs). EPA's initial hazard review for persistence, bioaccumulation and ecotoxicity indicated the need for the engineering assessment to evaluate potential releases to all media including water, air, landfill and incineration. Based on this information, the following assessment scope was selected.
Operations Assessed:
 Formulation of Metalworking Fluids
 Use of Metalworking Fluids
Releases assessed:
 Release to water
 Release to air
 Release to landfill
 Release to incineration

Assessment Approach
The release calculation methodology used in this assessment can be divided into two mains steps:
      1) Estimation of facility throughput of MCCPs/LCCPs in kg/site-yr and kg/site-day
      2) Estimation of the quantities of MCCPs/LCCPs released from the facility to a Publicly Owned Treatment Works (POTW), air, landfill or to incineration.

Facility Throughput
The first option for estimating facility throughput is to use site-specific information from the submitter. However, INEOS did not provide any site-specific information for facility throughputs. In this case, EPA used a generic site approach to estimate an average facility throughput. This value is derived from information on the production volume, estimates of the total number of sites and the days/yr of operation at a given site. Sources of these data include the PMN submission and EPA Generic Scenarios. Appendix E provides details on the basis used to estimate facility throughput values for each of the operations assessed.
Facility Releases (to POTW, air, landfill or incineration)
The first option for estimating facility releases (to POTW, air, landfill or incineration) is to use site-specific release information. However, INEOS did not provide any site-specific information in for these PMN substances. In this situation, EPA typically uses a loss fraction approach. Here, a loss fraction is applied to a facility daily use rate to estimate the amount of MCCPs or LCCPs released to a POTW, air, landfill or incineration. Loss fraction values are based on information in EPA generic scenarios and EPA/OPPT standard release assessment models.
Environmental Release Assessment
EPA's original environmental release assessment prepared in 2012 for these cases took a conservative approach to estimating environmental releases. EPA received additional information pertaining to the environmental release assessment in 2015 and also in 2016 in response to the 12/23/15 FR Notice requesting additional information on chlorinated paraffins PMNs.

In response to the additional information, EPA has expanded its release assessment approach to include additional environmental release assessment scenarios, in addition to the conservative approach from the 2012 analysis (Table 7). 

Table 7: Key assumptions in 2012 and 2016 expanded environmental release assessment.
#
Scenario
2012 Scenarios
2016 Expanded Assessment with Additional Release Assessment Scenarios
1
Formulation of Metalworking Fluid
Formulation into Water-Based Metalworking Fluids only
50/50 split between oil-based and water-based metalworking fluids

Equipment Cleaning Waste to uncertain media (POTW, landfill or incineration)
Oil-Based  -  equipment cleaning waste to landfill/incineration

For releases to POTW, assumed no on-site pre-treatment
Water-based  -  on-site pretreatment at 50%, 70% and 99% prior to POTW
2
Use of Metalworking Fluids
Used in Water-Based Metalworking Fluids only 
50/50 split between water-based metalworking fluids and oil-based metalworking fluids

All release sources released to POTW or uncertain (POTW, Incineration or Landfill)
Oil-Based fluids  -  per OECD Emission Scenario Document (ESD), only dragout releases to POTW. All other releases to incineration or landfill

Water releases discharged to POTW with no on-site pretreatment
Water-based fluids  -  on-site pretreatment at 50%, 70% and 99% efficiency prior to POTW
3
Plastics Compounding
Equipment cleaning release to water or incineration
Equipment cleaning release to incineration or landfill
4

Plastics Converting
Container cleaning release to uncertain media (POTW, incineration or landfill)
Solid compounded plastic residuals are handled as solid waste and released to incineration or landfill

Equipment cleaning release to uncertain media (POTW, incineration or landfill) 
Converted plastic residuals are handled as solid waste and released to incineration or landfill

Dust generation from trimming activities released to air (1%) and landfill (99%)
Dust generation from trimming activities released to POTW or landfill

Scrap material release to POTW or landfill 
Scrap material are handled as solid waste and released to incineration or landfill
5

Formulation of Adhesives and Sealants
Water releases discharged to POTW with no on-site pretreatment
On-site pretreatment at 50%, 70% and 99% efficiency prior to POTW

Off-Spec Material released to uncertain media (POTW, incineration or landfill) 
Off-Spec material released to incineration or landfill
6

Use of Adhesives and Sealants

Equipment Cleaning and Container Cleaning Waste to uncertain media (POTW, landfill or incineration)
No additional release assessment scenarios were done

Spray application of paints, adhesives and sealants
No change to application method

Summary of Release Assessment 
The engineering report with details on estimates, calculations and assumptions is provided in Appendix E. Tables 8 and 9 presents a summary of the environmental release assessment with respect to the potential for release to a POTW for P-12-0453, and 0433, respectively.

Table 8: Summary of environmental release assessment and potential for release to a POTW for P-12-0453.
                                       #
                                   Scenario
                     % of MCCP Throughput released to POTW
1
Formulation of Metalworking Fluids
                                       

Original (2012)
                                     4.89%

Oil-Based (2016)
                                      3%

Water-Based, 50% on-site pretreatment (2016)
                                      2%

Water-Based, 70% on-site pretreatment (2016) 
                                     1.2%

Water-Based, 99% on-site pretreatment (2016)
                                     0.04%

                                       
2
Use of Metalworking Fluids
                                       

Original (2012)
                                     92.2%

Oil-Based (2016)
                                     10.7%

Water-based 50% on-site pretreatment (2016)
                                     50.5%

Water-based 70% on-site pretreatment (2016)
                                     30.1%

Water-Based 99% pretreatment (2016)
                                     0.99%

                                       
3
Plastics Compounding
                                       

Original (2012)
                                      5%

Equipment Cleaning to Incineration or Landfill (2016)
                                      3%

                                       
4
Plastics Converting
                                       

Original (2012)
                                     5.49%

Solid Wastes from Equipment Cleaning, Container Cleaning, and Scrap Material to Incineration or Landfill; Dust Release to POTW or Landfill (2016)
                                     0.13%

                                       
5
Formulation of Adhesives and Sealants 
                                       

Original (2012)
                                     6.28%

Off-spec to incineration or landfill; 50% on-site pretreatment (2016)
                                     2.62%

Off-spec to incineration or landfill; 70% on-site pretreatment (2016)
                                     1.57%

Off-spec to incineration or landfill; 99% pretreatment (2016)
                                     0.05%

                                       
6
Use of Adhesives and Sealants  -  Original (2012)
                                     5.26%

Table 9: Summary of environmental release assessment and potential for release to a POTW for P-12-0433.
                                       #
                                   Scenario
                     % of LCCP Throughput released to POTW
1
Formulation of Metalworking Fluids
                                       

Original (2012)
                                      5%

Oil-Based (2016)
                                      3%

Water-Based, 50% on-site pretreatment (2016)
                                      2%

Water-Based, 70% on-site pretreatment (2016) 
                                     1.2%

Water-Based, 99% on-site pretreatment (2016)
                                     0.04%

                                       
2
Use of Metalworking Fluids
                                       

Original (2012)
                                     91.3%

Oil-Based (2016)
                                     10.3%

Water-based 50% on-site pretreatment (2016)
                                     49.5%

Water-based 70% on-site pretreatment (2016)
                                     29.7%

Water-Based 99% pretreatment (2016)
                                     0.99%

Modeled Environmental Concentrations
This section summarizes the approach used to estimate environmental concentrations using the scenarios described above.

Exposure pathways of interest for human health include drinking water, fish ingestion and air stack emissions. For aquatic organisms, the exposure pathway of concern is from direct releases to water. EPA/OPPT assessed each of these pathways by using the ChemSTEER ver. 2 release estimates as inputs to the Exposure and Fate Assessment Screening Tool (E-FAST V2.0) for estimating industrial releases and concentrations in the foregoing exposure pathways. 

EPA/OPPT assumed that potential releases to water occurred from indirect discharges to publicly owned treatment works (POTW). The E-FAST V2.0 modeling applied an assumption of 90% removal of MCCPs and LCCPs at the POTW. Water concentrations were estimated using E-FAST V2.0's probabilistic dilution model (PDM), which predicts downstream chemical concentrations from industrial discharges. These values were reported as the central tendency for a median flow site, a low flow site and the lowest seven-day average flow that occurs on average once every ten years (i.e., 7Q10). These estimated water concentrations were compared to the COC of 1 ug/L (rounded from the 1.2 ug/L presented in Table 4) for chronic aquatic invertebrates. Air stack emissions were estimated using generic scenarios, which assumed inhalation exposures occurring 100 meters downwind of a facility. It was further assumed that the CPs are degraded during incineration (ICPS, 1996), the preferred method for disposal of MCCPs (UK, 2008). In this report, EPA/OPPT estimated an incineration removal efficiency of 99.9% to calculate inhalation exposures to the general population downwind from incinerators that receive MCCPs/LCCPs in waste. EPA/OPPT used these estimated values for calculating human health and environmental risks of P-12-0453 and P-12-0433.

The results of the E-FAST V2.0 modeling are provided in Appendix F. Table 9 presents the values used in the risk assessment. As explained in the footnotes in Table 9, the values represent reasonable worst-case scenarios based on the processing and use scenarios presented in Table 7. However, these estimates require consideration of two important caveats: (1) limited environmental monitoring data are available and (2) MCCPs and LCCPs are expected to partition to particulates and sediment; however, E-FAST V2.0 models do not account for this partitioning.

                   Table 10: E-FAST Modeling Values Used[1]
                                   Scenario
                           Water Release - Human[2]
                            Air Release - Human[2]
                                       
                    Water Release  -  Aquatic Organisms[3]
                                       
                                       
                                Drinking Water
                                (mg/kg-bw/day)
                                Fish Ingestion
                                (mg/kg-bw/day)
                            Stack Air ADR (mg/m[3])
                          Fugitive Air ADR (mg/m[3])
                        Range of Concentrations (ug/L)
                              Days of exceed-ance
                                   P-12-0453
                Formulation of MWFs (Proc1  -  Four Scenarios)
Oil-Based
                               6.60 x 10[-][1]
                                2.17 x 10[+1]
                               1.58 x 10[-][2]
                               8.88 x 10[-][3]
                              799-5808 (29,600)*
                                      NA
Water-Based, 50% 
                               3.40 x 10[-][1]
                                1.14 x 10[+1]
                               8.30 x 10[-][3]
                               4.70 x 10[-][4]
                                 2.3-16.4 (84)
                                      239
Water-Based, 70% 
                               2.00 x 10[-][1]
                                 6.65 x 10[0]
                               4.92 x 10[-][3]
                               4.70 x 10[-][4]
                                1.4-9.9 (50.3)
                                      239
Water-Based, 99%
                               6.59 x 10[-][3]
                               2.20 x 10[-][1]
                               3.30 x 10[-][4]
                               8.88 x 10[-][3]
                                .045-0.33 (1.7)
                                      67
                     Use of MWFs (Use1  -  Four Scenarios)
Oil-Based
                               1.13 x 10[-][3]
                                2.20 x 10[-2]
                               9.30 x 10[-][5]
                                  No releases
                                0.47-5.9 (53)*
                                      210
Water-Based, 50% 
                               5.67 x 10[-][3]
                                1.10 x 10[-1]
                               4.26 x 10[-][5]
                                  No releases
                                 2.1-27 (242)
                                      244
Water-Based, 70% 
                               3.38 x 10[-][3]
                                6.60 x 10[-2]
                               2.54 x 10[-][5]
                                  No releases
                                1.3-16.1 (145)
                                      239
Water-Based, 99%
                               1.11 x 10[-][4]
                               2.17 x 10[-][3]
                               8.40 x 10[-][7]
                                  No releases
                               0.042-0.53 (4.8)
                                      70

Formulation: Plastics compounding (Proc2)
                               1.10 x 10[-][1]
                                 3.78 x 10[0]
                               2.75 x 10[-][3]
                               1.50 x 10[-][2]
                               0.053-0.39 (1.97)
                                      41
Use: Plastics converting (Use2)
                               8.06 x 10[-][5]
                                2.45 x 10[-3]
                                1.30 x 10[-4]
                               3.69 x 10[-][2]
                               0.021-0.66 (3.6)
                                      104
       Formulation of Adhesives and Sealants (Proc3  -  Four Scenarios)
Off-spec to incineration or landfill; 50% 
                               2.85 x 10[-][3]
                               9.44 x 10[-][2]
                               1.41 x 10[-][3]
                                  No releases
                                3.5-25.3 (129)
                                      200
Off-spec to incineration or landfill; 70%
                               1.71 x 10[-][3]
                               5.66 x 10[-][2]
                               1.39 x 10[-][3]
                                  No releases
                                 2.1-15.2 (77)
                                      199
Off-spec to incineration or landfill; 99%
                               5.71 x 10[-][2]
                                 1.89 x 10[0]
                               1.35 x 10[-][3]
                                  No releases
                               0.069-0.51 (2.6)
                                      82

Use of adhesives and sealants (Use3)
                               4.35 x 10[-][3]
                               7.50 x 10[-][2]
                               1.50 x 10[-][5]
                               1.60 x 10[-][1]
                                 0.26-3.0 (31)
                                      186
                                   P-12-0433
                 Formulation of MWFs (Use1  -  Four Scenarios)
Oil-Based
                               1.23 x 10[-][2]
                                3.80 x 10[-1]
                               3.50 x 10[-][4]
                                1.91 x 10[-3]
                               14.9-108.6 (554)*
                                      NA
Water-Based, 50% 
                               6.41 x 10[-][3]
                                2.00 x 10[-1]
                               1.60 x 10[-][4]
                                6.60 x 10[-4]
                                0.17-1.2 (6.2)
                                      41
Water-Based, 70% 
                               3.78 x 10[-][3]
                                1.20 x 10[-1]
                                1.0 x 10[-][4]
                                6.60 x 10[-4]
                               0.097-0.71 (36.1)
                                      31
Water-Based, 99%
                               1.25 x 10[-][4]
                               3.87 x 10[-][3]
                               1.58 x 10[-][5]
                               6.60 x 10[-][2]
                              0.0033-0.024 (0.12)
                                       0

                                       
                                       
                                       
                                       
                                0.15-1.1 (5.7)*
                                      NA

 Use of MWFs
Oil-Based
                               9.69 x 10[-][4]
                                1.76 x 10[-2]
                                8.42 x 10[-5]
                                  No releases
                                 0.4-5.1 (45)
                                      203
Water-Based, 50% 
                                4.68 x 10[-3]
                               8.52 x 10[-][2]
                                3.49 x 10[-5]
                                  No releases
                                1.9-24.4 (220)
                                      243
Water-Based, 70% 
                                2.81 x 10[-3]
                                5.11 x 10[-2]
                                2.09 x 10[-5]
                                  No releases
                                1.2-14.7 (132)
                                      237
Water-Based, 99%
                               9.45 x 10[-][5]
                                1.72 x 10[-3]
                                7.00 x 10[-7]
                                  No releases
                               0.039-0.49 (4.4)
                                      66
1 Taken from Appendix F. Values represent the highest concentrations/estimated doses (reported as the lifetime average daily dose, or LADD) for chronic (i.e., repeated exposure scenarios) for human health.
2 Estimated exposure values were corrected for absorption by the oral (50% absorption) and inhalation (50% absorption) routes of exposure (ECB 2005; EA 2009).
3 For PMNs, environmental risk was evaluated by performing a PDM as described above and in the E-FAST Manual (2007). The ranges encompass concentrations from the central tendency for a median flow site (e.g., 2.3 ug/L) up to the central tendency for a low flow site (e.g., 16.4 ug/L)  -  this example was taken from the third row (water-based, 50%) under P-12-0453 under the column heading "Range of Concentrations". The central tendency was calculated using the harmonic mean flow. The value in parentheses represents the 7Q10 (e.g., 84 ug/L) value normally used to determine potential chronic risk to aquatic organisms. 
NA indicates that there are not a sufficient number of days of release to calculate the days of exceedance where a chronic CoC was exceeded.
* The concentrations are based on a 24-hour average surface water concentration alone as the number of days of release was insufficient to model chronic surface water exposures.

OCCUPATIONAL EXPOSURE ESTIMATES

Assessment Scope
The operations assessed in the occupational exposure assessment were the same as for the modeled environmental release assessment describe above in Section 5.2. EPA estimates the number of workers potentially exposed and the potential for inhalation exposure (to vapors, particulates, aerosol/mists) and dermal exposure to the hands (through contact with liquids or solids). The scope of the occupational exposure assessment is summarized below.

	Operations Assessed:
               Formulation of Metalworking Fluids
               Use of Metalworking Fluids
               Plastics Compounding
               Converting of Compounded Plastics into Articles
               Formulation of Adhesives and Sealants
               Use of Adhesives and Sealants
	Occupational Exposures assessed:
               Number of workers potentially exposed
               Days per year for exposure
               Inhalation exposure (to vapors, particulates, aerosols, or mists) without use of respiratory protection
               Dermal exposure to the hands (through contact with liquids or solids) without the use of protective gloves

Assessment Approach
Number of workers

The approach involves estimating the number of sites and then estimating the number of workers potentially exposed per site. More details on how the approaches were applied to make estimates are provided in Apx E.

Number of sites

Site-Specific: Information provided to EPA in the PMN submission was used when available to estimate the number of sites for a given operation. 

Generic: In the absence of data and where the operation takes place at sites not under the submitter's control, EPA used a generic approach combining data from the PMN submission and data in generic scenarios. This involved three key parameters:

 Total Production Volume for the chemical (provided to EPA in the PMN submission)
 % of production volume for a given use (e.g., 74% for metalworking fluids)
 Estimate of the facility throughput (kg/site-yr) for a given operation described above in Section 5.2.2. 

Days/yr of Potential Exposure

EPA uses data provided in the PMN submission and generic scenarios as a basis to estimate days/yr of potential exposure. An often used default is to assume 250 days per year based on 50 weeks and 5 days per week.

Inhalation Exposure 

Quantitative Approach: The first option for estimating inhalation exposure is using monitoring data for the chemical being assessed or for analogous chemicals. These data may be provided in the PMN submission, available in generic scenarios or obtained from other published sources. In this assessment, such data were augmented with EPA assessment policy guidance to assess potential inhalation exposure. Table 11 summarizes the sources utilized for each operation assessed.
Personal Protective Equipment - EPA does not account for protection from use of respiratory protection in its screening-level assessments of inhalation exposure.

Table 11: Data sources for inhalation exposures.
                                   Operation
                   Source of Inhalation exposure assessment
Formulation of Metalworking Fluids (Proc1)
Negligible per EPA assessment policy for non-volatile liquids
Use of Metalworking Fluids (Use1)
Monitoring data for oil mist exposure in OECD Emission Scenario Document on Use of Metalworking Fluids 
PVC Compounding (Plastics Compounding) (Proc2)
Monitoring data for MCCP vapor exposure in published source
Converting of Compounded PVC into Articles (Use2)
Monitoring data for MCCP vapor exposure in published source
Formulation of Adhesives and Sealants (Proc3)
Negligible per EPA assessment policy for non-volatile liquids
Use of Adhesives and Sealants (Use3)
Standard EPA model for spray application of paints

Summary of Occupational Exposure Assessment
Table 12 below presents a summary of the occupational exposure estimates for P-12-0453 and 0433. No additional occupational exposure assessment work was performed for the scenarios in this 2016 assessment; the estimates presented below are the same as for the previous EPA risk assessment. 

Table 12: Summary of Occupational Exposure Estimates Used.
                                  Scenario[1]
                               Route of Exposure
                                       
                                  Inhalation
                                   (mg/day)
                                    Dermal
                                   (mg/day)
                                   P-12-0453
PROC1: Formulation of MWFs
                                    N/A[2]
                                 450  -  2,200
PROC2: PVC compounding 
                                 0.030  -  4.4
                                     2,200
PROC3: Formulation of adhesives and sealants
                                    N/A[2]
                                 660  - 2,200
USE1: Use of MWF
                                  2.0  -  7.1
                                 450  -  5,000
USE2: PVC converting
                                   12  -  22
                                    N/A[2]
USE3: Use of adhesives and sealants
                                      23
                                      530
                                   P-12-0433
PROC1: Formulation of MWFs
                                    N/A[2]
                                 450  -  2,200
USE1: Use of MWFs
                                  2.0  -  7.1
                                 450  -  3,900
[1]The following represent the estimated number of sites, workers per scenario and exposure over the course of the stated number of days: P-12-0453 = PROC1: 59 sites, 472 workers and 84 days/year; PROC2: 8 sites, 192 workers and 126 days/year; PROC3: 3 sites, 66 workers and 200 days/year; USE1: 207 sites, 9,936 workers and 247 days/year; USE2: 8 sites, 384 workers and 250 days/year; USE3: 58 sites, 2,784 workers and 250 days/year; P-12-0433 = PROC1: 3 sites, 24 workers and 27 days/year; USE1: 4 sites, 192 workers and 247 days/year.
[2]Not applicable, the use category does not result in exposures that are relevant for this route.

CONSUMER EXPOSURE ESTIMATES
INEOS did not identify consumer uses in its PMN applications for P-12-0453 and P-12-0433; therefore, EPA/OPPT did not perform an assessment for these types of exposures.
RISK ASSESSMENT

ENVIRONMENTAL ASSESSMENT
PMN risk assessments typically use modeled exposure values because, by definition, new chemical substances are not circulating in US commerce. However, for MCCPs and LCCPs, measured environmental data are available for some locations in the US and abroad. Though these data are not specific to P-12-0453 and P-12-0433, the data contain MCCP and LCCP congener groups that may be present in the PMN substances. However, EPA/OPPT used modeled exposure values as the principal source for its decision-making because the modeled exposure values were generated using exposure scenarios that are representative of the types of uses and releases that may occur with P-12-0453 and P-12-0433. In contrast, the measured environmental data are generally not amenable for identifying the types of uses or releases from which the measured congeners originated. Therefore, EPA/OPPT used these measured data as supporting information, along with modeled exposure values, to calculate potential environmental risks using the risk quotient (RQ) method. 

The RQ method integrates the results of exposure and ecotoxicity data (USEPA, 1998). 

An RQ is defined as:

               RQ = Environmental Concentration / Effect Level

where, the environmental concentration represents measured (see Tables 5 and 6) or estimated (see Table 10) values for each compartment (i.e., water, sediment and soil) and the effect level represents the COC for aquatic, benthic, or terrestrial species (see Table 4). 

An RQ greater than one serves as a benchmark for identifying whether aquatic concentrations of P-12-0453 and P-12-0433 may present a risk to aquatic- and sediment-dwelling organisms. 

Risk Estimates Using Environmental Monitoring Concentrations
The RQs shown in Table 13 suggest that measured concentrations of MCCPs and LCCPs in water and sediment may present an unreasonable risk of acute and chronic injury to aquatic organisms and may present an unreasonable risk of chronic injury to sediment-dwelling organisms. However, several limitations must be noted about the monitoring studies and the level of uncertainty that they contribute to the basis of these findings. First, the reported concentrations represent minimum and maximum values that span, at a minimum, several orders of magnitude and translate to RQs of less than one (i.e., low risk finding) or greater than one (i.e., risk finding), respectively. Second, the temporal and geographical distributions of these data, along with the different types of uses and releases that may have served as the originating sources, make it impossible to describe the central tendency of these data. Finally, the frequency and magnitude of locations with relevant use and release scenarios to the PMN substances, which may result in environmental releases of MCCPs or LCCPs that exceed the relevant COCs, is unknown. In addition to these general limitations, there are specific limitations and uncertainties that preclude using these values as the sole source from which to inform potential environmental concentrations and risks that may result from the specific uses and releases associated with P-12-0453 and P-12-0433. 

Table 13: Risk Quotients Calculated from Environmental Monitoring Data for Surface Water, Sediment and the Terrestrial Environment.

                          Environmental Concentration
                                 Effect Level 
                                  (i.e., COC)
                                      RQs
Acute Risk
Aquatic Species
                    < 2.50x10[-10] to 1.49x10[-3] mg/L
                                  0.001 mg/L
                         < 2.50x10[-7] to 1.49[1]
Chronic Risk
Aquatic Species
                    < 2.50x10[-10] to 1.49x10[-3] mg/L
                                  0.001 mg/L
                           < 2.50x10[-7] to 1.49
Chronic Risk
Sediment-dwelling Species
Non-marine Environment
                             0.002 to 65 mg/kg dw
                                 18.7 mg/kg dw
                              1.07x10[-4] to 3.5
Chronic Risk
Terrestrial Species
                              Insufficient Data 
                               14.9 mg/kg dw[2]
                                Not calculated
[1]Bolded values represent those that may present an unreasonable risk of injury.
[2] The COCs for terrestrial invertebrates and vertebrates were 14.9 mg/kg dw and 16.8 mg/kg diet, respectively. Since these values were comparable, EPA/OPPT used the lowest value as a potential means for calculating RQs for this compartment, once relevant data are available. 

For surface water, EPA/OPPT based the aquatic risk findings for MCCPs and LCCPs on the highest concentration reported by Petersen et al. (2006). These authors collected two surface water samples from an undisclosed location(s) in Norway and measured the concentration of MCCP congener groups (i.e., C14-17). The authors reported a concentration of 1.49 x 10[-3] mg/L for MCCP congener groups in one sample; however, a numerical value was not provided for the second sample, rather the distribution of congener groups was displayed in a bar graph. Based on the ordinate scale, the concentration of MCCP congener groups in the second sample was greater than zero, but less than 5.0 x 10[-4] mg/L. Of the monitoring studies reviewed by EPA/OPPT (see Appendix D), the Petersen et al. (2006) value of 1.49 x 10[-3] is the only surface water concentration that resulted in an RQ greater than one. All other surface water concentrations are at least one order of magnitude below 1.49 x 10[-3] mg/L (i.e., RQs < 1). 

For sediment concentrations, EPA/OPPT reviewed multiple studies, some of which reported values that exceeded the COC. Nicholls et al. (2001) reported the most relevant data for P-12-0453 and P-12-0433. These authors measured concentrations of MCCPs at locations in the United Kingdom where specific industries were known to employ MCCPs in the use categories identified for the PMN substances (e.g., lubricant in MWFs, plasticizer in PVC resins, and lubricant in sealants). Eight locations were sampled at three distances downstream (i.e., 100 meters, 300 meters, and 1-2 kilometers) from the respective sewage treatment works. At four of the locations, at least one of the sampled downstream values exceeded the COC (i.e., RQs > 1, risk finding). Though it is not possible to parse out the contribution of specific uses to the measured values, these data support that releases occur at locations with relevant uses to the PMN substances, which contribute to the environmental load of MCCP congener groups and in some cases result in RQs greater than one. 

For soil concentrations, EPA/OPPT was unable to calculate RQs for terrestrial organisms due to the absence of relevant measured data from biosolid-amended soils. Though Iozza (2010) and Wang et al. (2013) reported measured levels of MCCPs in soil, the samples were collected from sites in remote alpine locations or industrialized areas, respectively. These data are relevant for assessing airborne deposition of MCCPs/LCCPs; however, the reported concentrations are of questionable relevance with informing concentrations of MCCPs/LCCPs that may occur in biosolid-amended agricultural soils.

Due to the foregoing limitations and resulting uncertainties with the measured environmental data, EPA/OPPT used these data in a limited capacity for estimating potential risks associated with the use categories identified for P-12-0453 and P-12-0433. Specifically, these data were used as supporting information to inform the relevant pathways for estimating potential releases from relevant use categories for the PMN substances. A summary of the estimated release values and associated RQs that EPA/OPPT used as a key basis for evaluating the potential risks of P-12-0453 and P-12-0433 is presented in the following section. 
 
Risk Estimates Using Modeled Exposures 
The RQs shown in Table 14 suggest that, using the conventional EPA PMN method of using the 7Q10 flow scenario to represent the modeled concentration in water, all of the intended processes and uses for P-12-0453 and P-12-0433 are expected to result in releases to surface water at concentrations that may present an unreasonable risk of injury to aquatic organisms. 

Importantly, the Federal Register notice in 2015 requesting additional information regarding the use/removal/environmental release of CPs from the uses evaluated in this assessment resulted in significant changes for some water release/risk assessment calculations. Use of the submitted industry information pertaining to pre-treatment of MWFs (water -based vs. oil-based assumptions) resulted in declines in the 7Q10 estimate and the resulting estimate for risk. This was particularly evident when the median stream flow scenario is included in the range of risk estimates. For example, for P-12-0453, use of MWFs (Use1), the original EPA 2012 assessment predicted a median flow value of 0.47 ug/L and a 7Q10 flow of 53 ug/L; resulting in RQs of 0.47  -  53. When the water-based scenario is used (99% removal on-site, prior to release to POTW), the resulting range in RQs is 0.048  -  4.2. 

It is noteworthy that these estimated concentrations are within the range of measured surface water concentrations reported for MCCP congener groups (Table 5). Though there is uncertainty whether the form (i.e., dissolved or particle bound) of MCCP impacts the aquatic toxicity, the estimated values suggest that either form may exist. The median stream flow estimates are all below the reported water solubility for P-12-0453 and slightly above or below the water solubility reported for P-12-0433 (Table 1). Since the available aquatic toxicity data support that dissolved MCCP congener groups cause toxicity, the estimated water concentration values suggest that the risk finding for these scenarios are plausible. Some low stream flow and most 7Q10 flow scenarios estimate water concentrations that far exceed the estimated water solubility of all three PMN substances. Under these scenarios, the MCCP or LCCP congener groups would likely be bound to particulates and would eventually settle out in sediment. Nicholls et al. (2001) provided support for this pathway and showed that sediment concentrations of MCCP congener groups generally increased with distance downstream from the source outfall. Based on the foregoing information, EPA/OPPT concludes the following: 1) the estimated water concentrations were adequate for determining that environmental releases of P-12-0453 and P-12-0433 may present a risk of injury to aquatic organisms; and 2) it was unnecessary to estimate sediment concentrations of CP congener groups because any potential risks to sediment-dwelling organisms would be managed by addressing the risks identified for aquatic organisms.

Table 14: Risk Assessment of Aquatic Organisms Using Modeled Exposures[1]
                                   Scenario
                   Estimated Water Concentrations (ug/L)[2]
                                       
                                      RQs
                                       
                                Median Stream 
                                 Flow Scenario
                           Low Stream Flow Scenario
                                     7Q10 
                                 Flow Scenario
                              Days of exceedance
                                       
                                   P-12-0453
                Formulation of MWFs (Proc1  -  Four Scenarios)
Oil-Based
                                      799
                                     5808
                                    29,600
                                      NA
                                  799-29,600
Water-Based, 50% 
                                      2.3
                                     16.4
                                      84
                                      239
                                    2.3-84
Water-Based, 70% 
                                      1.4
                                      9.9
                                     50.3
                                      239
                                   1.4-50.3
Water-Based, 99%
                                     0.045
                                     0.33
                                      1.7
                                      67
                                   0.045-1.7
                     Use of MWFs (Use1  -  Four Scenarios)
Oil-Based
                                     0.47
                                      5.9
                                      53
                                      210
                                    0.47-53
Water-Based, 50% 
                                      2.1
                                      27
                                      242
                                      244
                                    2.1-242
Water-Based, 70% 
                                      1.3
                                     16.1
                                      145
                                      239
                                   1.3-16.1
Water-Based, 99%
                                     0.042
                                     0.53
                                      4.8
                                      70
                                   0.042-4.8

Plastics compounding (Proc2)
                                     0.053
                                     0.39
                                     1.97
                                      41
                                  0.053-1.97
Plastics converting (Use2)
                                     0.021
                                     0.66
                                      3.6
                                      104
                                   0.021-3.6
       Formulation of Adhesives and Sealants (Proc3  -  Four Scenarios)
Off-spec to incineration or landfill; 50% 
                                      3.5
                                     25.3
                                      129
                                      200
                                    3.5-129
Off-spec to incineration or landfill; 70%
                                      2.1
                                     15.2
                                      77
                                      199
                                    2.1-77
Off-spec to incineration or landfill; 99%
                                     0.069
                                     0.51
                                      2.6
                                      82
                                   0.069-2.6

Use of adhesives and sealants (Use3)
                                     0.26
                                      3.0
                                      31
                                      186
                                    0.26-31
                                   P-12-0433
                Formulation of MWFs (Proc1  -  Four Scenarios)
Oil-Based
                                     14.9
                                     108.6
                                      554
                                      NA
                                   14.9-554
Water-Based, 50% 
                                     0.17
                                      1.2
                                      6.2
                                      41
                                   0.17-6.2
Water-Based, 70% 
                                     0.097
                                     0.71
                                     36.1
                                      31
                                  0.097-36.1
Water-Based, 99%
                                    0.0033
                                     0.024
                                     0.12
                                       0
                                  0.033-0.12

                                     0.15
                                      1.1
                                      5.7
                                      NA
                                   0.15-5.7
                     Use of MWFs (Use1  -  Four Scenarios)
Oil-Based
                                      0.4
                                      5.1
                                      45
                                      203
                                    0.4-45
Water-Based, 50% 
                                      1.9
                                     24.4
                                      220
                                      243
                                    1.9-220
Water-Based, 70% 
                                      1.2
                                     14.7
                                      132
                                      237
                                    1.2-132
Water-Based, 99%
                                     0.039
                                     0.49
                                      4.4
                                      66
                                   0.039-4.4
[1]Taken from full model run of summary data presented in Appendix E.
[2]For PMNs, EPA/OPPT evaluated potential environmental risks by performing a PDM as described above and in the "Exposure and Fate Assessment Screening Tool (E-FAST) Version 2.0 Documentation Manual (2007)", available at: http://www.epa.gov/tsca-screening-tools/e-fast-exposure-and-fate-assessment-screening-tool-2014-documentation-manual 

HUMAN HEALTH
EPA/OPPT assessed potential risks to workers and the general population by calculating margins of exposure (MOE). This approach is performed according to the following equation:

          MOE = Point of Departure (POD) / Estimated human exposure

For the PODs, EPA/OPPT identified effect levels from three oral repeated dose toxicity studies, which served as the basis for calculating human equivalent doses (HEDs) (CXR 2005; NTP 1986). In the first study, CXR (2005) reported a NOAEL of 23 mg/kg-bw/day based on increased kidney weight at 222 mg/kg-bw/day in male rats exposed through diet for 90 days to an MCCP congener group (C14-17, 52 wt% Cl). In the second and third studies, NTP (1986) reported LOAELs of 100 mg/kg-bw/day based on granulomatous inflammation of the liver in female rats administered an LCCP congener (C23, 43 wt% Cl) by gavage for 5 days/week for 12 months or two years.

Using the effect levels of 23 mg/kg-bw/day (for the MCCP PMN: P-12-0453) or 100 mg/kg-bw/day (for the LCCP PMN [P-12-0433]), EPA/OPPT performed route-to-route extrapolations to develop HEDs for inhalation and dermal exposures in workers and for inhalation and oral exposures in the general population. EPA/OPPT did not assess oral exposures for workers, due to the unlikely nature of exposures occurring by this route. The respective HEDs served as the PODs for calculating MOEs, along with the previously reported estimated human exposure values for workers (Table 12) and the general population (Table 10). 
EPA/OPPT compared the MOEs to a benchmark value that consisted of a composite of three possible uncertainty factors (UFs): intraspecies variability (UFH; default value = 10), interspecies variability (UFA; default value = 10), and LOAEL-to-NOAEL extrapolation uncertainty (UFL; default value =10). The LOAEL-to-NOAEL extrapolation was only used for P-12-0433 (LCCP). The UFH and UFA may each be subdivided to account for toxicokinetics (TK; default value = 3.16) and toxicodynamics (TD; default value = 3.16). When effect levels from experimental animal studies are converted to HEDs, EPA/OPPT's default approach is to reduce the TK sub factor of UFA to 1 (i.e., UFA = TK x TD = 1 x 3.16 ≈ 3). 

EPA/OPPT interprets MOEs that were equal to or below a benchmark value (e.g., MOE < 1000 [UFH x UFA x UFL = 1000]) as an indication that the scenario(s) may present an unreasonable risk of injury to human health, whereas MOEs that were above the benchmark value is an indication of a low risk finding. When data are available that reduce these uncertainties, the benchmark MOEs may be lower. In the following sections, more detailed descriptions are provided on: 1) converting effect levels to route- and exposure-specific HEDs; 2) determining the appropriate UFs for the benchmark value, and 3) evaluating risk estimates for workers and the general population. 

Workers
EPA/OPPT performed route-to-route extrapolations to convert the oral NOAEL of 23 mg/kg-bw/day (i.e., MCCP congener groups) and the oral LOAEL of 100 mg/kg-bw/day (i.e., LCCP congener) to HEC values for inhalation exposures to workers (i.e., HECINHAL-WORKER) using the following equation (ECHA, 2012):

HECINHAL-WORKER = NOAELORAL or LOAELORAL x (1 / sRVRAT) x (ABSORAL-RAT / ABSINHAL- HUMAN) x (sRVHUMAN / wRV)
 
where, 	
      
      NOAELORAL = 23 mg/kg-bw/day (MCCP), or LOAELORAL = 100 mg/kg-bw/day (LCCP)
      sRVRAT = rat standard respiratory volume for 8-hours = 0.38 m[3]/kg bw
      ABSORAL-RAT = percent absorption by the oral route in rats = 50%
      ABSINHAL-HUMAN = percent absorption by inhalation in humans = 50%
      sRVHUMAN = human standard respiratory volume for 8-hours = 6.7 m[3]
      wRV = worker respiratory volume for 8-hours = 10 m[3]

For the oral NOAEL of 23 mg/kg-bw/day and the oral LOAEL of 100 mg/kg-bw/day, the HECINHAL-WORKER values equal 41 mg/m[3] and 176 mg/m[3], respectively. 

EPA/OPPT calculated the HED values for dermal exposures to workers (i.e., HEDDERM-WORKER) based on the following equation:

HEDDERM-WORKER = NOAELORAL x (ABSORAL-RAT / ABSDERMAL- HUMAN) x (BWHUMAN / BWRAT)[1/4]

where,

      NOAELORAL = 23 mg/kg-bw/day (MCCP), or LOAELORAL = 100 mg/kg-bw/day (LCCP)
      ABSORAL-RAT = percent absorption by the oral route in rats = 50%
      ABSDERM-HUMAN = percent absorption by the dermal route in humans = 1%
      BWRAT = rat bodyweight = 0.250 kg
      BWHUMAN = human bodyweight = 71.8 kg

The resulting HEDDERM-WORKER values equal 4,734mg/kg-bw/day for MCCP congener groups and 20,583 mg/kg-bw/day for the LCCP congener. 

EPA/OPPT used the foregoing HED values to inform the appropriate application of UFs to derive benchmark values. For MCCP congener groups and the LCCP congener, a benchmark value of 30 or 300 was applied, respectively. These values consisted of the following individual UFs. A default UFH of 10 was applied to each benchmark value, due to the absence of experimental data to inform the TK and TD sub factors of this UF. A reduced UFA of 3 was applied to each benchmark value, which accounted for a TK sub factor of 1 after converting the effect levels to HEDs (i.e., the use of allometric scaling). The UFA of 3 accounted for the remaining uncertainty associated with TD variability. A default UFL of 10 was only used for the benchmark value compared to the MOE derived from an LCCP congener because the underlying study reported a LOAEL, not a NOAEL. Thus, the acceptable MOE would be 30 (10 times 3) for MCCPs and 300 (10 times 10 times 3) for the LCCP.

EPA/OPPT used the HECINHAL-WORKER and HEDDERM-WORKER values for calculating the respective MOEs using the estimated exposure values presented in Table 12. As shown in Tables 15-18, the MOEs for P-12-0453 and P-12-0433 all exceeded the respective benchmark values, which indicate a finding of low risk to workers for the processes and uses evaluated in this assessment. 

When evaluating the risks of workers from exposure to MCCPs based on the available repeated-dose toxicology studies, the EU's draft Risk Assessment Report (RAR) on MCCPs concluded that except metal working fluids (MWF) use,  "There is at present no need for further information and/or testing or for risk reduction measures beyond those which are being applied already" (ECB, 2008).

Table 15: Occupational MOEs for P-12-0453 (MCCP): Inhalation Exposures (Hazard POD [HEC] = 41 mg/m[3])[1]
Scenario
                                Exposure Route
                           Modeled Exposure (mg/day)
                         Absorption Inhalation Human 
                   Inhalation Rate, Workers, Eight 
Hour/Day
                     Estimated Inhalation Exposure (mg/m3)
              Inhalation MOE (Risks Identified for MOEs < 30)
Proc 2
Inhalation
                                     0.03
                                      0.5
                                      10
                                    0.0015
                                     27333

                                      4.4
                                      0.5
                                      10
                                     0.22
                                      186
Use 1
Inhalation
                                       2
                                      0.5
                                      10
                                      0.1
                                      410

                                      7.1
                                      0.5
                                      10
                                     0.355
                                      115
Use 2
Inhalation
                                      12
                                      0.5
                                      10
                                      0.6
                                      68

                                      22
                                      0.5
                                      10
                                      1.1
                                      37
Use 3
Inhalation
                                      23
                                      0.5
                                      10
                                     1.15
                                      36
[1] Proc2 = Processing 2 = compounding of plastic products, Use 1 = use of metal working fluids, Use 2 = converting plastic products. Use 3 = use of adhesives and sealants. 

Table 16: Occupational MOEs for P-12-0453 (MCCP): Dermal Exposures (Hazard POD [HED] = 4734 mg/kg-bw/day)
Scenario
                                Exposure Route
                           Modeled Exposure (mg/day)
                                BW 
(E-FASTV2)
                           Absorption Dermal Human 
                   Estimated Dermal Exposure (mg/kg-bw/day)
               Dermal MOE  (Risks Identified for 
MOEs < 30)
Proc 1
Dermal
                                      450
                                     71.8
                                     0.01
                                     0.06
                                     75534

                                     2200
                                     71.8
                                     0.01
                                     0.31
                                     15450
Proc 2
Dermal
                                     2200
                                     71.8
                                     0.01
                                     0.31
                                     15450
Proc 3
Dermal
                                      660
                                     71.8
                                     0.01
                                     0.09
                                     51500

                                     2200
                                     71.8
                                     0.01
                                     0.31
                                     15450
Use 1
Dermal
                                      450
                                     71.8
                                     0.01
                                     0.06
                                     75534

                                     5000
                                     71.8
                                     0.01
                                     0.70
                                     6798
Use 3
Dermal
                                      530
                                     71.8
                                     0.01
                                     0.07
                                     64132
[1] Proc1 = Processing 1= Formulation of metal working fluids, Proc 2 = Processing 2 = compounding of rubber products, Use 1 = use of metal working fluids.

Table 17: Occupational MOEs for P-12-0433 (LCCP): Inhalation Exposures (Hazard POD [HEC] = 176 mg/m[3])[1]
Scenario
                                Exposure Route
                           Modeled Exposure (mg/day)
                         Absorption Inhalation Human 
                  Inhalation Rate,  Workers, Eight 
Hour/Day
                     Estimated Inhalation Exposure (mg/m3)
             Inhalation MOE  (Risks Identified for MOEs < 300)
Commercial Use of MWF
Inhalation
                                       2
                                      0.5
                                      10
                                      0.1
                                     1760

                                      7.1
                                      0.5
                                      10
                                     0.36
                                      489
                                       

                                       
                                       
                                       
                                       
                                       

                                       
                                       
                                       
                                       
Table 18: Occupational MOEs for P-12-0433 (LCCP): Dermal Exposures (Hazard POD [HED] = 20,583 mg/kg-bw/day)
Scenario
                                Exposure Route
                           Modeled Exposure (mg/day)
                                BW 
(E-FASTV2)
                           Absorption Dermal Human 
                   Estimated Dermal Exposure (mg/kg-bw/day)
               Dermal MOE  (Risks Identified for 
MOEs < 300)
Processing MWF
Dermal
                                      450
                                     71.8
                                     0.01
                                     0.06
                                    343050

                                     2200
                                     71.8
                                     0.01
                                     0.31
                                     66397
Commercial Use of MWF
Dermal
                                      450
                                     71.8
                                     0.01
                                     0.06
                                    343050

                                     3900
                                     71.8
                                     0.01
                                     0.54
                                     38117
                                       

General Population
EPA/OPPT converted the oral NOAEL of 23 mg/kg-bw/day (i.e., MCCP congener groups) and the oral LOAEL of 100 mg/kg-bw/day (i.e., LCCP congener) to HED values for oral exposures to the general population (i.e., HEDORAL-GENPOP) using the following equation:

HEDORAL-GENPOP = NOAELORAL x (ABSORAL-RAT / ABSORAL- HUMAN) x (BWHUMAN / BWRAT)[1/4] x (5 days / 7 days)[a]

where, 

      NOAELORAL = 23 mg/kg-bw/day (MCCP); or LOAELORAL=100 mg/kg-bw/day (LCCP)
      ABSORAL-RAT = percent absorption by the oral route in rats = 50%
      ABSORAL-HUMAN = percent absorption by the oral route in humans = 50%
      BWRAT = rat bodyweight = 0.250 kg
      BWHUMAN = human bodyweight = 71.8 kg
      [a]A duration-specific adjustment was applied because the animals were gavaged five days per week. 

For the oral NOAEL of 23 mg/kg-bw/day and the oral LOAEL of 100 mg/kg-bw/day, the HEDORAL-GENPOP values equal 67.6 mg/kg-bw/day and 294 mg/kg-bw/day, respectively. 

For assessing inhalation exposures to the general population, EPA/OPPT performed route-to-route extrapolations to convert the oral NOAEL of 23 mg/kg-bw/day (i.e., MCCP congener groups) and the oral LOAEL of 100 mg/kg-bw/day (i.e., LCCP congener) to HED values for inhalation exposures to the general population (i.e., HEDINHAL-GENPOP) using the following equation (ECHA, 2012):

HECINHAL-GENPOP = (NOAEL ORAL) x (1/sRVrat) x (ABSoral-rat/ABSinh-human) x 
(5 days/7 days)[a]

where,  

NOAELORAL = 23 mg/kg-bw/day (MCCP); or LOAELORAL=100 mg/kg-bw/day (LCCP)

sRVrat = rat standard respiratory volume for 24-hours = 1.15 m[3]/kg-bw

ABS ORAL-RAT = percent absorption by the oral route in rats = 50%
ABS INHAL-HUMAN = percent absorption by inhalation in humans = 50%
[a]A duration-specific adjustment was only applied because the animals were gavaged five days per week
                                       
For the oral NOAEL of 23 mg/kg-bw/day and the oral LOAEL of 100 mg/kg-bw/day, the HEDINHAL-GENPOP values equal 14.3 mg/m[3] and 62.1 mg/m[3], respectively. 

The same benchmark values of 30 or 300 were used for evaluating the general population MOEs. These benchmark values consisted of the same individual UFs and rationale discussed previously for workers. 

EPA/OPPT used the HEDORAL-GENPOP and HECINHAL-GENPOP values for calculating the respective MOEs using the estimated exposure values presented in Table 10. Tables 19 and 20 present risk estimates for all drinking water and fish ingestion scenarios for P-12-0453 and -0433.  There are three scenarios (out of 44) for which there is a potential risk to the general population due to fish ingestion using the E-FAST modeling results. These scenarios were further evaluated using the highest measured values of MCCPs in fish. The calculations, assumptions and results are also presented in Table 19. Using these measured values and high-end (95[th] percentile) fish intake assumptions, results in MOEs greater than 30 (i.e., 10,400). There are no risk concerns from exposure to the PMNs via drinking water. 

Though not used for determining risk, the three modeled fish ingestion scenarios where estimated risks were found are all for the MCCP (P-12-0453) and represent exposure from formulation of MWFs: from the oil-based assumption, the 50% pre-treatment assumption and the 70% pre-treatment assumption. There was no estimated risk from the MWF formulation with 99% the pre-treatment assumption. As with the environmental assessment, use of the submitted industry information pertaining to pre-treatment of MWFs (water -based vs. oil-based assumptions) resulted in declines in risk estimation, and, in this case (fish ingestion from formulation of MWFs), a scenario in which there was no estimated risk (i.e., 99% pre-treatment prior to release to a POTW).

Table 19: General Population MOEs for P-12-0453 (MCCP):  Drinking Water/Fish Ingestion Risk Estimates (Hazard POD [HED] = 67.6 mg/kg-bw/day)
Scenario 
                                Exposure Routes
                            Exposure (mg/kg bw/day)
                            Absorption Oral Human 
                       Estimated Exposure (mg/kg bw/day)
                                      MOE
                         (Risks Identified if <30)
Formulation of MWFs Oil-Based (Proc1) 
Drinking Water Ingestion
                                   6.60E-01
                                      0.5
                                    0.3300
                                      205

Fish Ingestion (b)[a]
                                     0.013
                                      0.5
                                    0.0065
                                    10,400

Fish Ingestion (m)[b]
                                   2.17E+01
                                      0.5
                                    10.8500
                                       6
MWF Formulation Water Based 50% Pretreatment (Proc1)
Drinking Water Ingestion
                                   3.40E-01
                                      0.5
                                    0.1700
                                      398

Fish Ingestion (b)
                                     0.013
                                      0.5
                                    0.0065
                                    10,400

Fish Ingestion (m)
                                   1.14E+01
                                      0.5
                                    5.7000
                                      12
MWF Formulation Water Based 70% Pretreatment (Proc1)
Drinking Water Ingestion
                                   2.00E-01
                                      0.5
                                    0.1000
                                      676

Fish Ingestion (b)
                                     0.013
                                      0.5
                                    0.0065
                                    10,400

Fish Ingestion (m)
                                   6.65E+00
                                      0.5
                                    3.3250
                                      20
MWF Formulation Water Based 99% Pretreatment (Proc1)
Drinking Water Ingestion
                                   6.59E-03
                                      0.5
                                    0.0033
                                     20516

Fish Ingestion
                                   2.20E-01
                                      0.5
                                    0.1100
                                      615
Use of MWF Oil based (Use1)
Drinking Water Ingestion
                                   1.13E-03
                                      0.5
                                    0.0006
                                    119646

Fish Ingestion
                                   2.20E-02
                                      0.5
                                    0.0110
                                     6145
Use of MWF Water Based 50% Pretreatment (Use1)
Drinking Water Ingestion
                                   5.67E-03
                                      0.5
                                    0.0028
                                     23845

Fish Ingestion
                                   1.10E-01
                                      0.5
                                    0.0550
                                     1229
Use of MWF Water Based 70% Pretreatment (Use1)
Drinking Water Ingestion
                                   3.38E-03
                                      0.5
                                    0.0017
                                     40000

Fish Ingestion
                                   6.60E-02
                                      0.5
                                    0.0330
                                     2048
Use of MWF Water Based 99% Pretreatment (Use1)
Drinking Water Ingestion
                                   1.11E-04
                                      0.5
                                   0.000056
                                    1218018

Fish Ingestion
                                   2.17E-03
                                      0.5
                                    0.0011
                                     62304
Plastics Compounding (Proc2)
Drinking Water Ingestion
                                   1.10E-01
                                      0.5
                                    0.0550
                                     1229

Fish Ingestion
                                   3.78E+00
                                      0.5
                                    1.8900
                                      36
Plastics Converting (Use2)
Drinking Water Ingestion
                                   8.06E-05
                                      0.5
                                    0.0000
                                    1677419

Fish Ingestion
                                   2.45E-03
                                      0.5
                                    0.0012
                                     55184
Formulation of Adhesives and Sealants Off-spec to incineration or landfill; 50% (Proc3)
Drinking Water Ingestion
                                   2.85E-03
                                      0.5
                                    0.0014
                                     47439

Fish Ingestion
                                   9.44E-02
                                      0.5
                                    0.0472
                                     1432
#5 Formulation of Adhesives and Sealants Off-spec to incineration or landfill; 70% (Proc3)
Drinking Water Ingestion
                                   1.71E-03
                                      0.5
                                    0.0009
                                     79064

Fish Ingestion
                                   5.66E-02
                                      0.5
                                    0.0283
                                     2389
#5 Formulation of Adhesives and Sealants Off-spec to incineration or landfill; 99% (Proc3)
Drinking Water Ingestion
                                   5.71E-02
                                      0.5
                                    0.0286
                                     2368

Fish Ingestion
                                   1.89E+00
                                      0.5
                                    0.9450
                                      72
 Use of Adhesives and Sealants (Use3)
Drinking Water Ingestion
                                   4.35E-03
                                      0.5
                                    0.0022
                                     31080

Fish Ingestion
                                   7.50E-02
                                      0.5
                                    0.0375
                                     1803
Shaded rows are scenarios with risk findings.
[a] B = "biota" to represent estimated fish ingestion based on highest reported levels of MCCPs in fish (i.e., 2.63 mg/kg-wet weight). See Table Apx_D-1-4 for levels of MCCPs in biota. Estimates for fish consumption is based on the Exposure Factors Handbook (US EPA, 2011). The highest 95[th] percentile value is used (4.9 grams of fish/kg-bw). The calculation for the three fish ingestion scenarios where modeled results suggest risk were refined using the following equation: 2.63 mg/kg-bw (MCCP concentration in fish) x 0.392 kg of fish intake = 1.03 mg/80 kg-bw = 0.013 mg/kg-bw.
[b]M = "modeled" to represent the estimated fish intake using E-FAST and associated assumptions. See Appendix F. 

Table 20: General Population MOEs for P-12-0433 (LCCP):  Drinking Water/Fish Ingestion Risk Estimates (Hazard POD [HED] = 294 mg/kg-bw/day)
Scenario 
                                Exposure Routes
                            Exposure (mg/kg bw/day)
                            Absorption Oral Human 
                       Estimated Exposure (mg/kg bw/day)
                                      MOE
                         (Risks Identified if <300)
Formulation of MWFs Oil-Based (Proc1) 
Drinking Water Ingestion
                                   1.23E-02
                                      0.5
                                    0.0062
                                     47805

Fish Ingestion
                                   3.80E-01
                                      0.5
                                    0.1900
                                     1547
MWF Formulation Water Based 50% Pretreatment (Proc1)
Drinking Water Ingestion
                                   6.41E-03
                                      0.5
                                    0.0032
                                     91732

Fish Ingestion
                                   2.00E-01
                                      0.5
                                    0.1000
                                     2940
MWF Formulation Water Based 70% Pretreatment (Proc1)
Drinking Water Ingestion
                                   3.78E-03
                                      0.5
                                    0.0019
                                    155556

Fish Ingestion
                                   1.20E-01
                                      0.5
                                    0.0600
                                     4900
MWF Formulation Water Based 99% Pretreatment (Proc1)
Drinking Water Ingestion
                                   1.25E-04
                                      0.5
                                    0.0001
                                    4704000

Fish Ingestion
                                   3.87E-03
                                      0.5
                                    0.0019
                                    151938
Use of MWF Oil based (Use1)
Drinking Water Ingestion
                                   9.69E-04
                                      0.5
                                    0.0005
                                    606811

Fish Ingestion
                                   1.76E-02
                                      0.5
                                    0.0088
                                     33409
Use of MWF Water Based 50% Pretreatment (Use1)
Drinking Water Ingestion
                                   4.68E-03
                                      0.5
                                    0.0023
                                    125641

Fish Ingestion
                                   8.52E-02
                                      0.5
                                    0.0426
                                     6901
Use of MWF Water Based 70% Pretreatment (Use1)
Drinking Water Ingestion
                                   2.81E-03
                                      0.5
                                    0.0014
                                    209253

Fish Ingestion
                                   5.11E-02
                                      0.5
                                    0.0256
                                     11507
Use of MWF Water Based 99% Pretreatment (Use1)
Drinking Water Ingestion
                                   9.45E-05
                                      0.5
                                   0.000047
                                    6222222

Fish Ingestion
                                   1.72E-03
                                      0.5
                                    0.0009
                                    341860

Tables 21 and 22 present the findings from estimating risk to the general population following inhalation exposure to each of the two PMN substances from either stack air or fugitive emissions. For all scenarios, the MOEs for P-12-0453 and -0433 all exceed the respective benchmark values, which indicate a finding of low risk to the general population from inhalation exposures (from either stack or fugitive sources of environmental release) that may occur due to the manufacturing, processing, and uses evaluated in this assessment.

Table 21: General Population MOEs for P-12-0453 (MCCP):  Inhalation Exposure to Stack/Fugitive Air Risk Estimates (Hazard POD [HEC] = 14.3mg/m[3]) 
                                   Scenario
                        (Either Stack or Fugitive Air)
                       Exposure Concentration (mg/m[3])
                          Absorption Inhalation Human
                                   (Percent)
                   Estimated Exposure Concentration (mg/m3)
                                      MOE
                         (Risks Identified if <30)
MWF Formulation Oil Based - Stack Air (Proc1)
                                   1.58E-02
                                      0.5
                                   7.90E-03
                                     1810
MWF Formulation Oil Based - Fugitive Air (Proc1)
                                   8.88E-03
                                      0.5
                                   4.44E-03
                                     3221
MWF Formulation Water Based 50% Pretreatment - Stack Air (Proc1)
                                   8.30E-03
                                      0.5
                                   4.15E-03
                                     3446
MWF Formulation Water Based 50% Pretreatment - Fugitive Air (Proc1)
                                   4.70E-04
                                      0.5
                                   2.35E-04
                                     60851
MWF Formulation Water Based 70% Pretreatment - Stack Air (Proc1)
                                   4.92E-03
                                      0.5
                                   2.46E-03
                                     5813
MWF Formulation Water Based 70% Pretreatment - Fugitive Air (Proc1)
                                   4.70E-04
                                      0.5
                                   2.35E-04
                                     60851
MWF Formulation Water Based 99% Pretreatment - Stack Air (Proc1)
                                   3.30E-04
                                      0.5
                                   1.65E-04
                                     86667
MWF Formulation Water Based 99% Pretreatment - Fugitive Air (Proc1)
                                   8.88E-03
                                      0.5
                                   4.44E-03
                                     3221
Use of MWF Oil based - Stack Air (Use1)
                                   9.30E-05
                                      0.5
                                   4.65E-05
                                    307527
Use of MWF Water Based 50% Pretreatment - Stack Air (Use1)
                                   4.26E-05
                                      0.5
                                   2.13E-05
                                    671362
Use of MWF Water Based 70% Pretreatment - Stack Air (Use1)
                                   2.54E-05
                                      0.5
                                   1.27E-05
                                    1125984
Use of MWF Water Based 99% Pretreatment - Stack Air (Use1)
                                   8.40E-07
                                      0.5
                                   4.20E-07
                                   34047619
Plastics Compounding - Stack Air (Proc2)
                                   2.75E-03
                                      0.5
                                   1.38E-03
                                     10400
Plastics Compounding -  Fugitive Air (Proc2)
                                   1.50E-02
                                      0.5
                                   7.50E-03
                                     1907
Plastics Converting - Stack Air (Use2)
                                   1.30E-04
                                      0.5
                                   6.50E-05
                                    220000
Plastics Converting - Fugitive Air (Use2)
                                   3.69E-02
                                      0.5
                                   1.85E-02
                                      775
Formulation of Adhesives and Sealants Off-spec to incineration or landfill 50% - Stack Air (Proc3)
                                   1.41E-03
                                      0.5
                                   7.05E-04
                                     20284
Formulation of Adhesives and Sealants Off-spec to incineration or landfill 70% - Stack Air (Proc3)
                                   1.39E-03
                                      0.5
                                   6.95E-04
                                     20576
Formulation of Adhesives and Sealants Off-spec to incineration or landfill 99% - Stack Air (Proc3)
                                   1.35E-03
                                      0.5
                                   6.75E-04
                                     21185
Use of Adhesives and Sealants - Stack Air (Use3)
                                   1.50E-05
                                      0.5
                                   7.50E-06
                                    1906667
Use of Adhesives and Sealants - Fugitive Air (Use3)
                                   1.60E-01
                                      0.5
                                   8.00E-02
                                      179

Table 22: General Population MOEs for P-12-0433 (LCCP):  Inhalation Exposure to Stack/Fugitive Air Risk Estimates (Hazard POD [HEC] = 62 mg/m[3]) 
Scenario
Exposure Concentration (mg/m[3])
Absorption Inhalation Human
Estimated Exposure Concentration (mg/m3)
                       MOE (Risks Identified if <300)
MWF Formulation Oil Based - Stack Air (Proc1)
                                   3.50E-04
                                      0.5
                                   1.75E-04
                                    354286
MWF Formulation Oil Based - Fugitive Air (Proc1)
                                   1.91E-03
                                      0.5
                                   9.55E-04
                                     64921
MWF Formulation Water Based 50% Pretreatment - Stack Air (Proc1)
                                   1.60E-04
                                      0.5
                                   8.00E-05
                                    775000
MWF Formulation Water Based 50% Pretreatment - Fugitive Air (Proc1) 
                                   6.60E-04
                                      0.5
                                   3.30E-04
                                    187879
MWF Formulation Water Based 70% Pretreatment - Stack Air (Proc1)
                                   1.00E-04
                                      0.5
                                   5.00E-05
                                    1240000
MWF Formulation Water Based 70% Pretreatment - Fugitive Air(Proc1) 
                                   6.60E-04
                                      0.5
                                   3.30E-04
                                    187879
MWF Formulation Water Based 99% Pretreatment - Stack Air(Proc1) 
                                   1.58E-05
                                      0.5
                                   7.90E-06
                                    7848101
MWF Formulation Water Based 99% Pretreatment - Fugitive Air (Proc1)
                                   6.60E-02
                                      0.5
                                   3.30E-02
                                     1879
Use of MWF Oil based - Stack Air
                                   8.42E-05
                                      0.5
                                   4.21E-05
                                    1472684
Use of MWF Water Based 50% Pretreatment - Stack Air
                                   3.49E-05
                                      0.5
                                   1.75E-05
                                    3553009
Use of MWF Water Based 70% Pretreatment - Stack Air
                                   2.09E-05
                                      0.5
                                   1.05E-05
                                    5933014
Use of MWF Water Based 99% Pretreatment - Stack Air
                                   7.00E-07
                                      0.5
                                   3.50E-07
                                   177142857

CONCLUSIONS
Based on its assessment of the available surrogate hazard and exposure information on P-12-0453 and P-12-0433, EPA/OPPT concludes the following pertaining to the manufacturing, processing and use of these PMN substances: 

 Occupational Exposures: Given the assumptions, data and scenarios evaluated in this assessment, there were no risks found for workers from either dermal or inhalation exposures to either of the PMN substances.
   2. General Population Exposures (from environmental releases): Given the assumptions, data and scenarios evaluated in this assessment, there were no risks found to humans from environmental releases via exposure to drinking water for either of the PMN substances, or from exposure via from fish ingestion (P-12-0433, the LCCP). There were three scenarios (3 out of 44) where potential risks to the general population due to fish ingestion were identified using the E-FAST modeling results. These scenarios were further evaluated using the highest measured values of MCCPs in fish. Using these measured values and high-end (95[th] percentile) fish intake assumptions, there were no risks identified. There were no risks found to humans from environmental releases via inhalation exposures from emissions from facilities for either PMN. 

 Environmental Assessment:
a. Using the conventional EPA PMN method of estimating water concentrations, all of the intended processes and uses for P-12-0453 and 0433 are expected to result in releases to the surface water at concentrations that may present an unreasonable risk following acute and chronic exposures to aquatic organisms. Use of additional information submitted in response to comments on a previous draft did result in decreases of estimated risk values for some scenarios.
   
b. Using available measured concentrations of MCCP and LCCP congener groups in the environment as supporting information, the PMN substances:
                   Are expected to partition to sediment and may partition to soil through land application of biosolids, and
                   May be released to the environment at water concentrations that may present an unreasonable risk following acute and chronic exposures to aquatic organisms.
                   May be released to the environment resulting in sediment concentrations that may present an unreasonable risk following chronic exposures to sediment organisms.
   
 PBT Assessment: The PMN substances may be very persistent and very bioaccumulative.

REFERENCES
Allpress, J. D., and P. C. Gowland. 1999. Biodegradation of Chlorinated Paraffins and Long-Chain Chloroalkanes by Rhodococcus Sp S45-1. International Biodeterioration and Biodegradation, 43(4), 173-179.

Arnot, Jon. 2013. Comments on Preliminary Bioaccumulation Assessment of Medium Chain
      Chlorinated Paraffins (MCCPs): Prepared for the MCCP REACH Consortium. April30, 2013.

Barber, J. L., A. J. Sweetman, G. O. Thomas, E. Braekevelt, G. A. Stern, and K. C. Jones. 2005. Spatial and Temporal Variability in Air Concentrations of Short-Chain (C-10-C-13) and Medium-Chain (C-14-C-17) Chlorinated N-Alkanes Measured in the UK Atmosphere. Environmental Science & Technology, 39(12), 4407-4415.

Bayen, S., J. P. Obbard, and G. O. Thomas. 2006. Chlorinated Paraffins: A Review of Analysis and Environmental Occurrence. Environment International, 32(7), 915-929.

Bengtsson, B. E., O. Svanberg, E. Linden, G. Lunde, and E. B. Ofstad. 1979. Structure Related Uptake of Chlorinated Paraffins in Bleaks (Alburnus-Alburnus L). Ambio, 8(2-3), 121-122.

Bennie, D. T., C. A. Sullivan, and R. J. Maguire. 2000. Occurrence of Chlorinated Paraffins in Beluga Whales (Delphinapterus leucas) from the St. Lawrence River and Rainbow Trout (Oncorhynchus mykiss) and Carp (Cyprinus carpio) from Lake Ontario. Water Quality Research Journal of Canada, 35(2), 263-281.

Bergman, A., A. Hagman, S. Jacobsson, B. Jansson, and M. Ahlman. 1984. Thermal-Degradation of Polychlorinated Alkanes. Chemosphere, 13(2), 237-250.

Birtley, R. D. N., D. M. Conning, J. W. Daniel, D. M. Ferguson, E. Longstaff, and A. A. B. Swan. 1980. The Toxicological Effects of Chlorinated Paraffins in Mammals. Toxicology and Applied Pharmacology, 54, 514-525.

       Boethling, R. S., P. H. Howard, J. A. Beauman, and M. E. Larosche. 1995. Factors for Intermedia Extrapolation in Biodegradability Assessment.  Chemosphere, 30, 741-752.
       
Borgen, A. R., M. Schlabach, and E. Mariussen. 2003. Screening of Chlorinated Paraffins in Norway. Organohalogen Compounds, 60, 331-334.

BRE (Building Research Establishment). 1994. Environmental Hazard Assessment: Chlorinated Paraffins. TSD/10. Directorate for Air, Climate and Toxic Substances; Toxic Substances Division, Garston, Watford, United Kingdom.

BUA (Beratergremium für Umweltrelevante Alstoffe). 1992. Chlorinated Paraffins: GCCH-Advisory Committe on Existing Chemicals of Environmental Relevence. BUA Report 93. (as cited in ECB, 2005 and IPCS, 1996).

Campbell, I., and G. McConnell. 1980. Chlorinated Paraffins and the Environment. 1. Environmental Occurrence. Environmental Science & Technology, 14(10), 1209-1214.

Chater, B. 1978. Acute Oral Toxicity, Skin and Eye Irritation and Skin Sensitisation. CTL/T/1168. Central Toxicology Laboratory, Alderley Park, Cheshire, UK.

Chen, M. Y., X. J. Luo, X. L. Zhang, M. J. He, S. J. Chen, and B. X. Mai. 2011. Chlorinated Paraffins in Sediments from the Pearl River Delta, South China: Spatial and Temporal Distributions and Implication for Processes. Environmental Science and Technology, 45(23), 9936-9943.

CMR. 1999. Chemical Profile: Chloroparaffins. Chemical Market Reporter, 33.

Coelhan, M. 2010. Levels of Chlorinated Paraffins in Water. CLEAN - Soil, Air, Water, 38(5-6), 452-456.

Coelhan, M., M. Saraci, and H. Parlar. 2000. A Comparative Study of Polychlorinated Alkanes as Standards for the Determination of C10-C13 Polychlorinated Paraffines in Fish Samples. Chemosphere, 40(6), 685-689.

Conz, A., and S. Fumero. 1988. Study of the Capacity of Solvocaffaro C1642 to Induce Gene Mutations in Strains of Salmonella Typhimurium. RBM Exp. No. 880367. Turin, Istituto di Recerche Biomediche "Antoine Marxer", Torino, Italy.

Cooley, H. M., A. T. Fisk, S. C. Wiens, G. T. Tomy, R. E. Evans, and D. C. Muir. 2001. Examination of the Behavior and Liver and Thyroid Histology of Juvenile Rainbow Trout (Oncorhynchus mykiss) Exposed to High Dietary Concentrations of C(10)-, C(11)-, C(12)- and C(14)-Polychlorinated N-Alkanes. Aquatic Toxicology, 54(1-2), 81-99.

CPA (Chlorinated Paraffins Association). 1994. Chlorinated Paraffin (52% Chlorinated, C14-17): Chronic Toxicity to Daphnia magna. Study conducted by Thompson, R. S., A. J. Banner, E. Gillings , and N. R. Gore, Brixham Environmental Laboratory: ZENECA Limited, (February 16, 1994), Brixham, UK. OTS 0573997. Doc ID 88000000085.

CPA (Chlorinated Paraffins Association). 1996. Chlorinated Paraffin (52% Chlorinated, C14-17): Chronic Toxicity to Daphnia magna. Study conducted by Thompson, R. S., A. J. Banner, E. Gillings , and N. R. Gore, Brixham Environmental Laboratory: ZENECA Limited, (October 2, 1996), Brixham, UK. OTS 0573997. Doc ID 88000000085.

CPC (Chlorinated Paraffin Consortium). 1980. Initial Investigation into the Aquatic Toxicity of Chlorinated Paraffins. Study conducted by Madeley, J. R. , and C. R. Pearson, Imperial Chemical Industries PLC, Brixham Laboratory, Brixham, Devon, UK. DCN 88920006972.

CPC (Chlorinated Paraffins Consortium). 1983a. Toxicity of Chlorinated Paraffin to Mussels (Mytilus edulis) over 60 Days; [52% Chlorination of Intermediate Chain Length N-Paraffin]. Study conducted by Madeley, J. R., R. S. Thompson, D. V. Smyth, D. Taylor, E. Gillings, B. J. Harland , and R. I. Cumming, Imperial Chemical Industries PLC, Brixham Laboratory, Brixham, Devon, UK. OTS# 0507258. DCN 408332184.

CPC (Chlorinated Paraffin Consortium). 1983b. Toxicity of Chlorinated Paraffin to Rainbow Trout over 60 Days; 52% Chlorination of Intermediate Chain Length N-Paraffins. Study conducted by Madeley, J. R., B. G. Maddock, J. E. Caunter, D. Taylor, E. Gillings, B. J. Harland , and R. I. Cumming, Imperial Chemical Industries PLC, Brixham Laboratory, Brixham, Devon, UK. OTS# 0507258. DCN 408332184.

CPIA (Chlorinated Paraffins Industry Association). 2013. Use and Benefits of CPs. Washington, DC. http://www.regnet.com/cpia/benefits.html.

CXR (CXR Biosciences Ltd). 2003. Effects of Medium Chain Chlorinated Paraffins (MCCPs) on Vitamin K Concentrations and Clotting Factors in Fematle Sprague Dawley Rats. Powrie, R.H., CXR Biosciences Ltd, Dundee, UK.

CXR (CXR Biosciences Ltd). 2004. MCCP-Study to Assess Maternal Milk and Neonate Plasma. Barton, S.J. and Daly, P.M., CXR Biosciences Ltd, Dundee, UK.

CXR (CXR Biosciences Ltd). 2005. Study to Investigate the Elimination of Medium Chain Chlorinated Paraffins in Male F344 Rats. CXR0204. Elcombe, B.M., Dundee, UK.

CXR (CXR Biosciences Ltd). 2006. C14-17 N-Alkane, 52% Chlorinated Study of Post-Natal Offspring Mortality Following Dietary Administration to Cd Rats. DAR0001/062390. Stamp, S.L., CXR Biosciences Ltd, Dundee, UK.

de Boer, C. 2010. Chlorinated Paraffins in The Handbook of Environmental Chemistry 10. editor: C. de Boer  ISBN-10: 364210760

DEPA (The Danish Environmental Protection Agency). 2014. Survey of Short-Chain and Medium-Chain Chlorinated Paraffins. Lassen, C.; Sorensen, G.; Crookes, M.; Christensen, F; Jeppesen, C.N.; Warming, M.; Mikkelsen, S.H.; Nielsen, J.M., Copenhagen, Denmark.

Dick, T. A., C. P. Gallagher, and G. Tomy. 2010. Short- and Medium-Chain Chlorinated Paraffins in Fish, Water and Soils from the Iqaluit, Nunavut (Canada), Area. World Review of Science, Technology and Sustainable Development, 7, 387-401.

EA (Environment Agency). 2009. Using Science to Create a Better Place. Environmental Risk Assessment: Long-Chain Chlorinated Paraffins. SCHO0109BPGR-E-E. Environment Agency, United Kingdom, West Almondsbury, Bristol.

EC (Environment Canada). 1993. Priority Substances List Assessment Report: Chlorinated Paraffins. EN 40 215/17E. Health and Welfare Canada, Ottawa, Ontario, Canada. http://bibvir1.uqac.ca/archivage/000169030.pdf.

EC (Environment Canada). 1995. Occurrence of Chlorinated Paraffins in the St. Lawrence River near a Manufacturing Plant in Cornwall, Ontario. NWRI Contribution 95-62. National Water Research Institute, Aquatic Ecosystems Protection Branch, Burlington, Ontario.

EC (Environment Canada). 2008a. Follow-up Report on a PSL1 Assessment for Which Data Were Insufficient to Conclude Whether the Substances Were "Toxic" to the Environment and to the Human Health. Chlorinated Paraffins.

EC (Environment Canada). 2008b. Priority Substances List Assessment Report: Chlorinated Paraffins. Environment Canada.

ECB (European Chemicals Bureau). 2000. European Union Risk Assessment Report-Alkanes, C10-13, Chloro (SCCP). Joint Research Center, Institute for Health and Consumer Protection, European Chemicals Bureau, European Union, United Kingdom.

ECB (European Chemicals Bureau). 2005. European Union Risk Assessment Report-Alkanes,C14-17, Chloro (MCCP). Joint Research Center, Institute for Health and Consumer Protection, European Chemicals Bureau, European Union, United Kingdom.

ECB (European Chemicals Bureau). 2008. Draft European Union Risk Assessment Report: Alkanes, C14-17, Chloro (Medium-Chained Chlorinated Paraffins). Cas No: 85535-85-9. EINECS No: 287-477-0. Joint Research Center, Institute for Health and Consumer Protection, European Chemicals Bureau, Bootle, Merseyside.

      ECHA (European Chemicals Agency). 2012. Guidance on information requirements and chemical safety assessment. Chapter R.8: Characterization of dose [concentration]-response for human health. Available at:  https://echa.europa.eu/documents/10162/13632/information_requirements_r8_en.pdf/e153243a-03f0-44c5-8808-88af66223258 

Elliott, B. M. 1989. Meflex Dc029 (Fully Formulated) - Ames Test. CTL/L2668. Imperial Chemical Industries Ltd, Macclesfield, Cheshire, UK.

Engels, H.-W., H.-J. Weidenhaupt, M. Pieroth, W. Hofmann, K.-H. Menting, T. Mergenhagen, R. Schmoll, and S. Uhrlandt. 2000. Rubber, 9. Chemicals and Additives. In Ullmann's Encyclopedia of Industrial Chemistry. Wiley-VCH Verlag GmbH & Co. KGaA. http://dx.doi.org/10.1002/14356007.a23_365.pub3.

Fisk, A. T., C. D. Cymbalisty, A. Bergman, and D. C. G. Muir. 1996. Dietary Accumulation of C-12- and C-16-Chlorinated Alkanes by Juvenile Rainbow Trout (Oncorhynchus mykiss). Environmental Toxicology and Chemistry, 15(10), 1775-1782.

Fisk, A. T., G. T. Tomy, C. D. Cymbalisty, and D. C. G. Muir. 2000. Dietary Accumulation and Quantitative Structure-Activity Relationships for Depuration and Biotransformation of Short (C-10), Medium (C-14), and Long (C-18) Carbon-Chain Polychlorinated Alkanes by Juvenile Rainbow Trout (Oncorhynchus mykiss). Environmental Toxicology and Chemistry, 19(6), 1508-1516.

Fisk, A. T., G. T. Tomy, and D. C. G. Muir. 1999. Toxicity of C10-, C11-, C12-, and C14-Polychlorinated Alkanes to Japanese Medaka (Oryzias latipes) Embryos. Environmental Toxicology and Chemistry, 18(12), 2894-2902.

Fisk, A. T., S. C. Wiens, G. R. B. Webster, W. Bergman, and D. C. G. Muir. 1998. Accumulation and Depuration of Sediment-Sorbed C-12- and C-16-Polychlorinated Alkanes by Oligochaetes (Lumbriculus variegatus). Environmental Toxicology and Chemistry, 17(10), 2019-2026.

Frank, U. 1993. Okotoxizitat Von Chloroparaffinen. Institut fur Wasser-Boden und Lufthygiene. (EA, 2009).

Frank, U., and F. Steinhauser. 1994. Okotoxizitat Schwerloslicher Stoffgemische Am Biespiel Der Dapnientoxizitat Von Chloroparaffinen. Vom Wasser, 83, 203-211. (EA, 2009).

Fridén, U. E., M. S. McLachlan, and U. Berger. 2011. Chlorinated Paraffins in Indoor Air and Dust: Concentrations, Congener Patterns, and Human Exposure. Environment International, 37(7), 1169-1174.

Friedman, D., and P. Lombardo. 1975. Photochemical Technique for Elimination of Chlorinated Aromatic Interferences in Gas-Liquid-Chromatographic Analysis for Chlorinated Paraffins. Journal of the Association of Official Analytical Chemists, 58(4), 703-706.

Funke, W., L. Hoppe, J. Hasselkus, L. G. Curtis, K. Hoehne, H.-J. Zech, P. Heiling, M. Yamabe, K. Dören, H. Schupp, R. Küchenmeister, M. Schmitthenner, W. Kremer, W. Wieczorrek, H. Gempeler, W. Schneider, J. W. White, A. G. Short, W. J. Blank, L. J. Calbo, D. Plath, F. Wagner, W. Haller, and K.-M. Rödder. 2010. Paints and Coatings, 2. Types. In Ullmann's Encyclopedia of Industrial Chemistry. Wiley-VCH Verlag GmbH & Co. KGaA. http://dx.doi.org/10.1002/14356007.o18_o01.

Greenpeace. 1995. Greenpeace Zur Sache: Chlorparaffine.

Hart, D., G. Wickramaratne, S. De, P. Banham, I. Chart, and B. Gaskell. 1985. Chlorinated Paraffin (52% Chlorination of Intermediate Chain Length N-Paraffins): Investigation into the Possible Mechanism of Haemorrhage in Offspring Rats. CTL/P/1293. ICI Central Toxicology Laboratory, Alderley Park, Cheshire, UK.

Health Canada. (2011). Update on the Human Health Assessment of Long-Chain Chlorinated Alkanes. 

Health and Environment Canada (1993). Canadian Environmental Protection Act. Priority Substances List Assessment Report. Chlorinated paraffins. Government of Canada.

Hildebrecht, C. O. 1972. Biodegradability Study on Chlorinated Waxes. Laboratory Report No. 50-0405-001. Environlab Inc., Plainesville, OH.

Hilger, B., H. Fromme, W. Volkel, and M. Coelhan. 2013. Occurrence of Chlorinated Paraffins in House Dust Samples from Bavaria, Germany. Environmental Pollution, 175, 16-21.

Hoechst, A. G. 1976. Unveroffentlichte Untersuchung (19.5.1976).

Hoechst, A. G. 1977. Unveroffentlichte Untersuchung (28.11.1977).

Houde, M., D. C. Muir, G. T. Tomy, D. M. Whittle, C. Teixeira, and S. Moore. 2008. Bioaccumulation and Trophic Magnification of Short- and Medium-Chain Chlorinated Paraffins in Food Webs from Lake Ontario and Lake Michigan. Environmental Science & Technology, 42(10), 3893-3899.

Hüttig, J. 2006. Determination of the "New" Problem Group Chloroparaffins in Sediments by HRGC-LRMS. (Ph.D. dissertation), Univeristy of Basel, Basel, Switzerland, pp.149.

Hüttig, J., and M. Oehme. 2005. Presence of Chlorinated Paraffins in Sediments from the North and Baltic Seas. Archives of Environmental Contamination and Toxicology, 49(4), 449-456.

Hüttig, J., and M. Oehme. 2006. Congener Group Patterns of Chloroparaffins in Marine Sediments Obtained by Chloride Attachment Chemical Ionization and Electron Capture Negative Ionization. Chemosphere, 64(9), 1573-1581.

Hüttig, J., Z. Zencak, and M. Oehme. 2004. Levels of Chlorinated Paraffins in North and Baltic Sea Sediments. Organohalogen Compounds, 66, 1321-1326.

Iozza, S. 2010. A Survey of the Spatial, Altitudinal, and Temporal Distribution of Chlorinated Paraffins in the Alpine Region. (Ph.D. dissertation, Thesis number 9128), University of Basel, Switzerland, pp.1-114.

Iozza, S., C. E. Muller, P. Schmid, C. Bogdal, and M. Oehme. 2008. Historical Profiles of Chlorinated Paraffins and Polychlorinated Biphenyls in a Dated Sediment Core from Lake Thun (Switzerland). Environmental Science & Technology, 42(4), 1045-1050.

IPCS (International Programme on Chemical Safety). 1996. Environmental Health Criteria 181, Chlorinated Paraffins. World Health Organization, Switzerland. http://www.inchem.org/documents/ehc/ehc/ehc181.htm.

IRDC (International Research and Development Corporation). 1981. Chlorinated Paraffin: Range-Finding Teratology Study in Rats. IRDC Report No. 438/034. Mattawan, Michigan, USA.

IRDC (International Research and Development Corporation). 1982. Chlorinated Paraffin: Range-Finding Teratology Studies in Rabbits. IRDC Report No. 438/036. Mattawan, Michigan, USA.

IRDC (International Research and Development Corporation). 1983. Chlorinated Paraffin: Teratology Study in Rabbits. IRDC Report No. 438/032. Mattawan, Michigan, USA.

IRDC (International Research and Development Corporation). 1984. Chlorinated Paraffin: Teratology Study in Rats. 438/017. Mattawan, Michigan, USA.

IRDC (International Research and Development Corporation). 1985. Chlorinated Paraffin: Reproduction Range-Finding Study in Rats. IRDC Report No. 438/049. Mattawan, Michigan, USA.

IVL (IVL Swedish Environmental Research Institute). 2009. Screening of Selected Hazardous Substances in the Eastern Baltic Marine Environment. IVL Report B1874. Stockholm, Sweden.

Johnson, I. 2005. Cereclor S52: In Vitro Absorption through Human Epidermis. CTL.JV1833/REG/REPT. Central Toxicology Laboratory, Alderley Park, Cheshire, UK.

Johnson, W. W., and M. T. Finley. 1980. Handbook of Acute Toxicity of Chemicals to Fish and Aquatic Invertebrates: Summaries of Toxicity Tests Conducted at Columbia National Fisheries Research Laboratory, 1965-78. Resource Publication 137. United States Department of the Interior, Fish and Wildlife Service, Washington, D.C.

Kemmlein, S., A. Hermeneit, and W. Rotard. 2002. Other Halogenated POPs of Concern: Carbon Skeleton Analysis of Chloroparaffins in Sediment, Mussels and Crabs. Organohalogen Compounds, 59, 279-282.

Koh, I. O., and W. Thiemann. 2001. Study of Photochemical Oxidation of Standard Chlorinated Paraffins and Identification of Degradation Products. Journal of Photochemistry and Photobiology a-Chemistry, 139(2-3), 205-215.

Linden, E., B. E. Bengtsson, O. Svanberg, and G. Sundstrom. 1979. Acute Toxicity of 78 Chemicals and Pesticide Formulations against 2 Brackish Water Organisms, the Bleak (Alburnus alburnus) and the Harpacticoid nitocra-spinipes. Chemosphere, 8(11-12), 843-851.

Lombardo, P., J. L. Dennison, and W. W. Johnson. 1975. Bioaccumulation of Chlorinated Paraffin Residues in Fish Fed Chlorowax 500c. Journal of the Association of Official Analytical Chemists, 58(4), 707-710.

Madeley, J. R., and R. D. N. Birtley. 1980. Chlorinated Paraffins and the Environment .2. Aquatic and Avian Toxicology. Environmental Science & Technology, 14(10), 1215-1221.

Madeley, J. R., and B. G. Maddock. 1983a. The Bioconcentration of a Chlorinated Paraffin in the Tissues and Organs of Rainbow Trout (Salmo gairdneri). Brixham Confidential Report No. BL/B/2310. Brixham, Imperial Chemical Industries Ltd, Brixham Laboratory.

Madeley, J. R., and B. G. Maddock. 1983b. Effects of a Chlorinated Paraffin on the Growth of Rainbow Trout. Chlorinated Paraffin: 58% Chlorination of Short Chain Length Paraffins. Brixham Confidential Report No. BL/B/2309. Brixham , Imperial Chemical Industries Ltd, Brixham Laboratory.

Madeley, J. R., and R. S. Thompson. 1983. Toxicity of Chlorinated Paraffins to Mussels (Mytilus edulis) over 60 Days. Chlorinated Paraffin: 58% Chlorination of Short Chain Length N-Paraffins. Brixham Confidential Report No. BL/B/2291. Brixham, Imperial Chemical Industries Ltd, Brixham Laboratory.

Mayer, F. L., and M. R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resource Publication No. 160. US Dept. of the Interior, Fish and Wildlife Service, Washington, DC.

ME (Ministry of the Environment). 2003. Chemicals in the Environment in 2002. Environmental Health and Safety Division, Environmental Health Department, Ministry of the Environment, Japan.

Medeiros, A. S., C. E. Luszczek, J. Shirley, and R. Quinlan. 2011. Benthic Biomonitoring in Arctic Tundra Streams: A Community-Based Approach in Iqaluit, Nunavut, Canada. Arctic, 64(1), 59-72.

Muir, D. 2010. Environmental Levels and Fate. In Boer, J. d., Chlorinated Paraffins. Handbook of Environmental Chemistry (Vol. 10, pp. 107-133). Springer-Verlag, Berlin.

Muir, D., E. Braekevelt, G. Tomy, and M. Whittle. 2003. Medium Chain Chlorinated Paraffins in Great Lakes Food Webs. Organohalogen Compounds, 64, 166-169.

Muir, D., G. Stern, and G. Tomy. 2000. Chlorinated Paraffins. In Paasivirta, J., The Handbook of Environmental Chemistry Vol. 3 Part K New Types of Persistent Halogenated Compounds (Vol. 3,  Chapter 8, pp. 203-236). Springer-Verlag, Berlin.

Murmann, P. 1988. The Testing of the Skin-Sensitising Effect of Chloroparaffin 40g (Containing 1% Stabiliser B74) in the Guinea Pig. Huls AG Report No. 1336. Huls AG, Marl, Germany.

Nicholls, C. R., C. R. Allchin, and R. J. Law. 2001. Levels of Short and Medium Chain Length Polychlorinated N-Alkanes in Environmental Samples from Selected Industrial Areas in England and Wales. Environmental Pollution, 114(3), 415-430.

NRC (National Research Council). 2000. Toxicological Risks of Selected Flame-Retardant Chemicals. National Academies. http://www.nap.edu/catalog/9841.html.

NTP (National Toxicology Program). 1986. Toxicology and Carcinogenesis Studies of Chlorinated Paraffins (C23, 43% Chlorine) in F344/N Rats and B6C3F1 Mice (Gavage Studies). TR-305. National Toxicology Program, Research Triangle Park, NC.

NTP (National Toxicology Program). 1986. Toxicology and Carcinogenesis Studies of Chlorinated Paraffins (C12, 60% Chlorine) in F344/N Rats and B6C3F1 Mice (Gavage Studies). TR-305. Research Triangle Park, NC, USA.

OECD (Organization for Economic Co-Operation and Development). 2004. Emission Scenario Document on Additives in Plastics Processing (Compounding) Draft. U. S. Environmental Protection Agency.

OECD (Organization for Economic Co-operation and Development). 2004. Emission Scenario Document on Additives in Plastic Processing (Converting into Finished Products) Draft. U.S. Environmental Protection Agency.

OECD (Organization for Economic Co-Operation and Development). 2014. Emission Scenario Document on Additives in Plastics Processing (Compounding) Revised Draft. U. S. Environmental Protection Agency.

OECD (Organization for Economic Co-operation and Development). 2014. Emission Scenario Document on Additives in Plastic Processing (Converting into Finished Products) Revised Draft. U.S. Environmental Protection Agency.

OECD (Organization for Economic Co-operation Development). 2009. Emission Scenario Document on Plastics Additives.

OECD (Organization for Economic Co-operation Development). 2009. Emission Scenario Document on Adhesives Formulation.

OECD (Organization for Economic Co-operation Development). 2008. Emission Scenario Document on Adhesives Use.

OECD (Organization for Economic Co-operation Development). 2011. Emission Scenario Document on the Use of Metalworking Fluids.

Olofsson, U., A. Bignert, and P. Haglund. 2012. Time-Trends of Metals and Organic Contaminants in Sludge. Water Research, 46, 4841-4851.

Omori, T., T. Kimura, and T. Kodama. 1987. Bacterial Cometabolic Degradation of Chlorinated Paraffins. Applied Microbiology and Biotechnology, 25(6), 553-557.

Pellizzato, F., M. Ricci, A. Held, H. Emons, W. Bohmer, S. Geiss, S. Iozza, S. Mais, M. Petersen, and P. Lepom. 2009. Laboratory Intercomparison Study on the Analysis of Short-Chain Chlorinated Paraffins in an Extract of Industrial Soil. Trac-Trends in Analytical Chemistry, 28(8), 1029-1035.

Petersen, M., P. Bussmann, R. Grumping, and G. Liek. 2006. Analysis of Short-Chain (C10-C13) and Medium-Chain Chlorinated Paraffins (C14-C17) in Norwegian Sediment and Water Samples by GC/ECNI-Ms. Organohalogen Compounds, 68, 2101-2104.

Phipps, G. L., G. T. Ankley, D. A. Benoit, and V. R. Mattson. 1993. Use of the Aquatic Oligochaete Lumbriculus variegatus for Assessing the Toxicity and Bioaccumulation of Sediment-Associated Contaminants. Environmental Toxicology and Chemistry, 12(2), 269-279.

Poon, R., P. Lecavalier, P. Chan, C. Viau, H. Hakansson, I. Chu, and V. E. Valli. 1995. Subchronic Toxicity of a Medium-Chain Chlorinated Paraffin in the Rat. Journal of Applied Toxicology, 15(6), 455-463.

Pribylova, P., J. Klanova, and I. Holoubek. 2006. Screening of Short- and Medium-Chain Chlorinated Paraffins in Selected Riverine Sediments and Sludge from the Czech Republic. Environmental Pollution, 144(1), 248-254.

PVC. 2013. PVC Additives. http://www.pvc.org/en/p/pvc-additives.

Renberg, L., M. Tarkpea, and G. Sundstrom. 1986. The Use of the Bivalve Mytilus edulis as a Test Organism for Bioconcentration Studies. Ii. The Bioconcentration of Two [14]C-Labeled Chlorinated Paraffins. Ecotoxicology and Environmental Safety, 11, 361-372.

Reth, M., A. Ciric, G. N. Christensen, E. S. Heimstad, and M. Oehme. 2006. Short- and Medium-Chain Chlorinated Paraffins in Biota from the European Arctic -- Differences in Homologue Group Patterns. The Science of the Total Environment, 367(1), 252-260.

Reth, M., Z. Zencak, and M. Oehme. 2005. First Study of Congener Group Patterns and Concentrations of Short- and Medium-Chain Chlorinated Paraffins in Fish from the North and Baltic Sea. Chemosphere, 58(7), 847-854.

Scott, R. 1984. In Vitro Absorption of [14]C Cereclor S52 through Human Skin. CTL/L/758. Central Toxicology Laboratory, Alderley Park, Cheshire, UK.

Serrone, D.M. Birtley, R.D.N., Weigand, W. and Millischer, R. (1987). Toxicology of Chlorinated Paraffins. Food and Chemical Toxicology. 25: 553-562.

Stevens, J. L., G. L. Northcott, G. A. Stern, G. T. Tomy, and K. C. Jones. 2003. PAHs, PCBs, PCNs, Organochlorine Pesticides, Synthetic Musks, and Polychlorinated N-Alkanes in U.K. Sewage Sludge: Survey Results and Implications. Environmental Science and Technology, 37(3), 462-467.

Tarkpea, M., E. Linden, B. E. Bengtsson, A. Larsson, and O. Svenberg. 1981. Products Control Studies at the Brackish Water Toxicology Laboratory 1979-80. NBL Report 1981-03-23. Swedish Environmental Protection Agency, Nykoping, Sweden.

Thomas, G. O., E. Braekevelt, G. Stern, F. L. Martin, and K. C. Jones. 2003. Further Work on Chlorinated Paraffins in Human Milk-Fat. A Report on a Research Project Funded by the Eurochlor Chlorinated Paraffin Sector Group. Department of Environmental Sciences, Lancaster University, Lancaster University, UK.

Thomas, G. O., and K. C. Jones. 2002. Chlorinated Paraffins in Human and Bovine Milk-Fat. CLT/T/831. ICI Central Toxicology Laboratory, Alderley Park, Cheshire, UK.

Thompson, R., and M. Vaughan. 2014. Medium-Chain Chlorinated Paraffins (MCCPs): A Review of Bioaccumulation Potential in the Aquatic Environment. Integrated Environmental Assessment and Management, 10(1), 78-86.

Thompson, R. S. 2002. Medium-Chain Chlorinated Paraffin (52% Chlorinated, C14-17): Effect in Soil on Nitrogen Transformation by Soil Microorganisms. AstraZeneca Confidential Report BL7466/B.

Thompson, R. S. 2007. Statistical Review of: TNO Report: IMW-R 93-018 "Semi-Static Reproduction Test with Chlorinated Paraffins and Daphnia magna (OECD Guideline No. 202". Personal communication from Euro Chlor. (EA, 2009).

Thompson, R. S., J. E. Caunter, and E. Gillings. 2000. Medium-Chain Chlorinated Paraffin (51% Chlorinated N-Pentadecane-8-[14]C): Bioconcentration and Elimination by Rainbow Trout (Oncorhynchus mykiss). AstraZeneca Confidential Report BL6869/B. AstraZeneca.

Thompson, R. S., and N. R. Gore. 1999. Chlorinated Paraffin (52% Chlorinated, C14-17): Acute Toxicity to Two Freshwater Crustaceans, Gammarus Pulex and Daphnia magna. Unpublished Report, BLS2643/B.

Thompson, R. S., D. V. Smyth, and E. Gillings. 1997. Chlorinated Paraffin (52% Chlorinated, C14-17): Toxicity to the Green Alga Selenastrum capricornutum. AstraZeneca Confidential Report, BL 5791/B.

Thompson, R. S., D. V. Smyth, and E. Gillings. 2002. Medium-Chain Chlorinated Paraffin (52% Chlorinated, C14-17): Effects in Sediment on the Survival, Growth and Sexual Development of the Freshwater Amphipod, Hyalella azteca. AstraZeneca Confidential Report BL7469/B.

Thompson, R. S., N. J. Williams, and E. Gillings. 1997. Chlorinated Paraffin (52% Chlorinated, C14-C17): Chronic Toxicity to Daphnia magna. AstraZeneca Confidential Report, BL 5791/B.

Thompson, R. S., A. J. Windeat, and E. Gillings. 2001a. Medium-Chain Chlorinated Paraffin (52% Chlorination, C14-17): Effects in Sediment on Emergence of the Midge, Chironomus riparius. AstraZeneca Confidential Report BL7093/B 

Thompson, R. S., A. J. Windeat, and E. Gillings. 2001b. Medium-Chain Chlorinated Paraffin (52% Chlorination, C14-17): Effects in Sediment on the Survival, Growth, and Reproduction of the Freshwater Oligochaete, Lumbriculus variegates. AstraZeneca Confidential BL7090/B 

Thompson, R. S., A. J. Windeat, and E. Gillings. 2001c. Medium-Chain Chlorinated Paraffin (52% Chlorination, C14-17): Effects in Soil and Seed Germination and Vegetative Growth of Wheat (Triticum aestivum), Oilseed Rape (Brassica napus) and Mung Bean (Phaseolus aureus). AstraZeneca Confidential Report BL7128/B.

Thompson, R. S., A. J. Windeat, and E. Gillings. 2001d. Medium-Chain Chlorinated Paraffin (52% Chlorination, C14-17): Effects in Soil on the Survival, Growth, and Reproduction of the Earthworm, Eisenia fetida. AstraZeneca Confidential Report BL7115/B.

TNO. 1993. Semi-Static Reproduction Test with Chlorinated Paraffins and Daphnia magna (OECD Guideline No. 202). TNO Report IMW-R 93-018. TNO Institute of Environmental Sciences, Delft, the Netherlands. 

Tomy, G., A. T. Fisk, J. B. Westmore, and D. Muir. 1998. Environmental Chemistry and Toxicology of Polychlorinated N-Alkanes. Reviews of Environmental Contamination and Toxicology, 158, 53-128.

Tomy, G., and G. Stern. 1999. Analysis of C14-C17 Polychloro-N-Alkanes in Environmental Matrixes by Accelerated Solvent Extraction-High-Resolution Gas Chromatography/Electron Capture Negative Ion High-Resolution Mass Spectrometry. Analytical Chemistry, 71, 4860-4865.

Tomy, G., G. Stern, W. Lockhart, and D. Muir. 1999. Occurrence of C10-C13 Polychlorinated N-Alkanes in Canadian Midlatitude and Arctic Lake Sediments. Environmental Science & Technology, 33, 2858-2863.

Tomy, G. T. 2010. Analysis of Chlorinated Paraffins in Enviromental Matrices: The Ultimate Challenge for the Analytical Chemist. In Boer, J. d., Chlorinated Paraffins. Handbook of Environmental Chemistry (Vol. 10, pp. 83-106). Springer-Verlag, Berlin.

Tomy, G. T., D. C. G. Muir, G. A. Stern, and J. B. Westmore. 2000. Levels of C-10-C-13 Polychloro-N-Alkanes in Marine Mammals from the Arctic and the St. Lawrence River Estuary. Environmental Science & Technology, 34(9), 1615-1619.

Tsunemi, K. 2010. Risk Assessment of Short-Chain Chlorinated Paraffins in Japan. In Boer, J. d., The Handbook of Environmental Chemistry Chlorinated Paraffins (Vol. 10, pp. 155-194). Springer Berlin Heidelberg, Safety Executive Industrial Chemicals Unit, Berlin, Germany. http://dx.doi.org/10.1007/698_2009_35.

USEPA (U.S. Environmental Protection Agency). 1988. Chlorinated Paraffins: A Report on the Findings from Two Field Studies, Sugar Creek, Ohio and Tinkers Creek Ohio. EPA 560/5-87-012. Office of Toxic Substances, Exposure Evaluation Division, Washington, DC.

USEPA (U.S. Environmental Protection Agency). 1998. Guidelines for Ecological Risk Assessment. EPA/630/R-95/002F. Risk Assessment Forum, Washington, DC http://www.epa.gov/raf.

USEPA (U.S. Environmental Protection Agency). 1999. Determining the Adequacy of Existing Data (Draft).

USEPA (U.S. Environmental Protection Agency). 2012. Sustainable Futures P2 Framework Manual. US EPA, Office of Chemical Safety and Pollution Prevention. EPA-748-B12-001. http//www.epa.gov/opt/sf/pubs/sf-p2-manual.html 

USEPA (U.S. Environmental Protection Agency). 2014. Framework for Human Health Risk Assessment to Inform Decision Making. EPA/100/R-14/001. Office of the Science Advisor, Risk Assessment Forum, Washington, DC. http://www.epa.gov/raf.

van Ginkel, C. G. 2010a. Biodegradability of a C14-17 Medium Chain Chlorinated Paraffin (63.2% Cl W/W) in the Closed Bottle Test. AkzoNobel confidential report: T10008c. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G. 2010b. Biodegradability of C14-17 Chlorinated Paraffin (45.6% Cl) in the Closed Bottle Test. AkzoNobel confidential report: T10007c. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G. 2010c. Biodegradability of Medium-Chain Chlorinated Paraffin (51.7% Cl W/W) in the Closed Bottle Test. AkzoNobel confidential report: T10031c. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G. 2010d. Biodegradability of Polychlorinated Tetradecane (45%) in the Closed Bottle Test. AkzoNobel confidential report 2.397.140. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G. 2014a. Biodegradability of C15 Chlorinated N-Alkane, 51% Cl (Wt.) in the Closed Bottle Test (OECD TG 301). AkzoNobel confidential report: F 14024 CG; Study number: T13029c. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G. 2014b. Biodegradability of C15 Chlorinated N-Alkane, 51% Cl (Wt.) in the Closed Bottle Test (OECD TG 301d). AkzoNobel confidential report: F 14025 CG; Study Number T13030c. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G., and A. Louwerse. 2010a. Biodegradability of Chlorinated Tetradecane in Closed Bottle Tests Incoluated with Activated Sludge and River Water. AkzoNobel confidential report 2.427.188. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

van Ginkel, C. G., and A. Louwerse. 2010b. Evaluation of the Ultimate Biodegradability of Chlorinated Tetradecanes Using in Sequencing Batch Reactors. AkzoNobel confidential report: 2.427.189. AkzoNobel Technology and Engineering, Arnhem, The Netherlands.

Wang, Y., J. Li, Z. Cheng, Q. Li, X. Pan, R. Zhang, D. Liu, C. Luo, X. Liu, A. Katsoyiannis, and G. Zhang. 2013. Short- and Medium-Chain Chlorinated Paraffins in Air and Soil of Subtropical Terrestrial Environment in the Pearl River Delta, South China: Distribution, Composition, Atmospheric Deposition Fluxes, and Environmental Fate. Environmental Science and Technology, 47(6), 2679-2687.

Wiegand, W. 1989. Determination of the Mutagenic Effects of Chloroparaffin 40g. AM-89/08. Huls AG, Huls AG, Marl, Germany.

Willis, B., M. J. Crookes, J. Diment, and S. D. Dobson. 1994. Environmental Hazard Assessment: Chlorinated Paraffins. TD170.9, G7ts, no. 19. Department of the Environment, Toxic Substances Division of the Directorate for Air, Climate and Toxic Substances, Garston, Watson, UK.

Zeng, L. X., H. J. Li, T. Wang, Y. Gao, K. Xiao, Y. G. Du, Y. W. Wang, and G. B. Jiang. 2013. Behavior, Fate, and Mass Loading of Short Chain Chlorinated Paraffins in an Advanced Municipal Sewage Treatment Plant. Environmental Science & Technology, 47(2), 732-740.

APPENDICES

 ENVIRONMENTAL FATE AND BIOACCUMULATION STUDY SUMMARIES

 ENVIRONMENTAL PERSISTENCE
 Abiotic Degradation
Generally, CPs are stable to hydrolysis and to direct photolysis in air and water, though very limited data exist on hydrolysis and direct and indirect photolysis in soil, water, or air. In studies using aliphatic hydrocarbon solvents, CPs were shown to be poor absorbers of UV light and no direct photodegradation was observed (Friedman and  Lombardo, 1975; Lombardo et al., 1975).
Koh and Thiemann (2001) studied photolysis of aqueous solutions for CPs products with chain lengths ranging from C10 to C24 including an MCCP product, Hoechst CP52, with chain lengths from C12 to C18 and an average of 52 wt% Cl. A mercury vapor lamp with main radiation wavelengths of 254, 302, 313, 366,405/408, and 436 was used in batch experiments. Following a 5 hour radiation time, estimated atmospheric degradation rates showed photolysis half-lives of less than 20 hours based on measurement of free chloride and analysis of degradation products. The MCCP product had a T1/2 of 12.8 hour in aqueous solution. The addition of peroxide or acetone increased the photolysis rate suggesting that indirect photolysis may be significant. The authors also reported that longer chain CPs were formed during this study and speculated that recombination of smaller alkyl radicals could occur under some conditions. 

Thermal degradation data for MCCPs and LCCPs are limited, but studies of SCCPs and Polyvinyl chlorides suggest MCCPs are degraded rapidly at 250 - 350 °C (Bergman et al., 1984). Dehydrohalogenation may lead to the formation of a large number of aliphatic and aromatic compounds. Chlorine radical formation can lead to production of highly chlorinated aromatics including polychlorinated biphenyls. Higher Cl content results in production of greater numbers and amounts of chlorinated aromatics (Bergman et al., 1984).

 Fate in Air
As noted above, CPs lack structural components that absorb light in the UV or visible spectrum, so direct photolysis is not expected to occur. The atmospheric half-life has been estimated at 1 - 2 days (EA, 2009; ECB, 2005), based on estimated values for the second order rate constant for reaction with atmospheric hydroxyl radicals for MCCPs with lower chlorine contents between 40 and 56 wt%. EPA/OPPT also estimated atmospheric half-lives for MCCPs (40 and 70 wt% Cl) calculated using EPI Suite(TM)/AOPWIN(TM) (v. 1.92a) that range from about 1 to > 4 days (see Table_Apx A-1). MCCPs with the shorter chain lengths and higher chlorine contents were calculated to be more persistent. 

MCCPs have low estimated vapor pressures (4.5 x 10[-8] to 2.27 x 10[-3] Pa at 20 - 25°C) and a Henry's law constant (HLC) (0.014 - 51.3 Pa x m[3]/mol for C14-17 congener groups) and are not expected to partition to air. They may be transported associated with particulate matter, and have been reported in indoor and outdoor air and house dust (Barber et al., 2005; Fridén et al., 2011; Hilger et al., 2013). Wide spread soil contamination and occurrence in artic samples suggest that MCCPs behave similarly to other chlorinated persistent organic pollutants (POPs) with high production volumes and releases, and are subject to long range transport (Dick et al., 2010; Medeiros et al., 2011; Tomy et al., 2000). 

                    Table_Apx A-1: Estimated Atmospheric Half Lives Using EPI Suite(TM)/AOPWIN(TM) (v. 1.92a) for Varying MCCP Chain Length and Chlorination Percents Based on Wt. 
                                 Chain Length
                                  40 wt% Cl 
                                  70 wt% Cl 
                                      C14
                                      1.0
                                      4.4
                                      C15
                                      0.8
                                      3.0
                                      C16
                                      0.8
                                      3.0
                                      C17
                                      0.8
                                      2.9

 Biodegradation
EPA/OPPT reviewed studies from the open literature and submitted to EPA/OPPT including those described in the Canada and EU assessments and referenced in Table_Apx A-2 (EC, 2008a; ECB, 2005) to determine biodegradation under a variety of environmental conditions. Some of these studies used modified test conditions to enhance or maximize biodegradation. EPA/OPPT concurs with the EU's conclusions that under these modified test conditions, C14 41.3% by wt. Cl and a C14 45.5% by wt. Cl substances are readily biodegradable. C 15 51% by wt. Cl were found to be inherently degradable and possibly readily degradable in modified OECD 301 and 301D tests. This suggests that CPs with these chain lengths and shorter, and this degree of chlorination and lower, are inherently degradable. More highly chlorinated and longer carbon chain CPs (C14-17 51.7% by wt. Cl, C14 55% by wt. Cl, C14 60.2% by wt. Cl, and C14 -17 63.2% by wt. Cl) biodegraded over a range of 2-54% in 28 days to 4-57% at up to 60 days. The most highly chlorinated, (C14-17, 63.2 wt% Cl) biodegraded 5% in 28 days and 10% at 60 days in the enhanced biodegradation studies, suggesting that longer chain and higher chlorination can contribute to greater persistence under most environmental conditions. (Van Ginkel, 2014 a and b; Van Ginkel 2010 a-d; Van Ginkel and Louwerse 2010 a and b).
 Fate in Wastewater Treatment
In its review of the available measured data on MCCPs in wastewater treatment from data in from other countries, EPA/OPPT determined that CPs are present in the majority of municipal waste water treatment plant (WWTP) influent (Coelhan, 2010; Nicholls et al., 2001; Stevens et al., 2003; Zeng et al., 2013). Low water solubility and relatively high partitioning coefficients suggest that most of the MCCPs and LCCPs entering WWTP systems will associate with solids. Some biodegradation of shorter chain, lower chlorinated MCCP congener groups may occur, while longer chain length, more chlorinated congener groups will be resistant to aerobic and anaerobic degradation. Shorter and lower chlorinated congener groups have higher vapor pressure and may be lost to the vapor phase during aeration. WWTP effluent also contains some particulate-associated MCCPs. Because of their low water solubility, little MCCP or LCCP will be in the dissolved phase, and the majority will be removed along with settled sludge. Once associated with the sludge, the CPs will generally be stable in sludge treatment and remain in the residual biosolids. Land application of biosolids will transfer the MCCPs and LCCPs to agricultural and other soils (Nicholls et al., 2001; Stevens et al., 2003). Because 50 - 60% of biosolids in the US are land applied, the majority of MCCPs and LCCPs entering WWTPs may be released to the environment via application to soil, and may be transported from contaminated soil to other locations and media by soil erosion, runoff, and wind borne particulates, and volatilization.

 Fate in Surface Water, Sediments and Groundwater
Because they generally have low water solubility, high sorption coefficients, and tend to partition to solids, MCCPs and LCCPs released to surface water will partition to surficial sediment where they may be buried and removed from potential degradation processes. This explains what is found in the limited monitoring data that exist - MCCP concentrations in surface water are generally in the low pg/L range, while sediment concentrations are several orders of magnitude higher (EC, 2008a).  The presence could also be partially due to the general observation of slower rates of biodegradation under anaerobic conditions, as can occur in sediments, than under aerobic conditions (Boethling et al. 1995). Applying this observation to the rates of aerobic biodegradation for certain MCCPs reported elsewhere in this document suggests they may be persistent or very persistent in anaerobic environments.   

MCCPs may leach from soil and be transported to groundwater, but low solubility and high sorption will act to keep dissolved concentrations very low. Facilitated transport with colloids and particulates may occur so that MCCPs can be transported in groundwater, but in general, concentrations in this compartment are expected to be very low. MCCPs that are introduced to groundwater will tend to partition to the solid phase and not be mobile.
 Fate in Soil 
Existing monitoring data suggest that MCCPs are present in soil, probably as a result of atmospheric transport and deposition. Areas near sources, such as land receiving wastewater biosolids, manufacturing and processing facilities, and electronic waste processing and recycling facilities are shown to have higher levels (Wang et al., 2013). MCCPs are expected to be stable in soil, and once deposited, could remain/persist in the soil for years or decades. Burial and advective transport away from the site of deposition are the major dissipation processes. No data are available on soil photolysis, although aqueous photolysis data suggest that indirect photolysis may result in degradation to shorter and less chlorinated CP congener groups. No soil biodegradation data exists, but some strains of bacteria that can co-metabolize MCCPs have been identified (Allpress and  Gowland, 1999). If degradation does occur, it is expected to be slow with T1/2 of at least months to years.

Table_Apx A-2: Review of MCCP and LCCP Biodegradation Studies.

 Overall Conclusions for Table_Apx A-2: Based on the studies summarized below, it is concluded that constituents including those of C 14-17 63% Cl, C 14-17, 60-63% Cl, C 14-17 51%, and 53-56% Cl, C14 60.2 %Cl, and  C 18-20 48 - 70% Cl may be persistent or very persistent.

Table_Apx A-2: Biodegradation Studies on MCCPs (C14-17) and LCCPs (C>18) 
                                 Study Authors
                               Publication Date
            MCCP/LCCP Chemicals Evaluated (i.e., C-length, wt% Cl)
                                    Method
                                Study Duration
                      Noteworthy Results and Implications
                                     MCCPs
                                  Van Ginkel
                                     2010d
                                 C14 45 wt% Cl
                                 Closed bottle
                                    28 days
Approximately 64% degraded in 28 days
Based on oxygen demand
                                  Van Ginkel
                                     2010b
                              C14-17 45.6 wt% Cl
                                 Closed bottle
                                    28 days
Approximately 51% in 28 days and 63% in 42 days degradation
Based on oxygen demand
                                  Van Ginkel
                                     2010c
                              C14-17 51.7 wt% Cl
                                 Closed bottle
                                    28 days
Approximately 27% degradation in 28 days and 57% after 60 days 
Based on oxygen demand
                                  Van Ginkel
                                     2010a
                              C14-17 63.2 wt% Cl
                                 Closed bottle
                                    28 days
Approximately 5% degradation after 28 days and 10% after 60 days. 
                            Van Ginkel and Louwerse
                                     2010a
                        C14 45,50,55,60, 60.2 wt% Cl %
              Closed bottle with river water and sludge inoculum
                                    28 days
Approximately 40% (60.2 wt%Cl) degradation in 84 days in sludge, 21% degradation in 105 days in river water
                           Van Ginkel and Louwerse 
                                     2010b
                         C14 41.3,45.5, 50, 60 wt% Cl
                                 Batch reactor
                                21 and 105 days
41.3 wt% Cl: 79% degradation in 21 days and 94% at 105 days.
50 wt% Cl: 14% degradation by
21 days, 5 % in 80 days. 60 wt% Cl <10% degradation in 80 days based on quantitation of released chloride
Conclusions: Quantification of degradation was by oxygen uptake or chloride release. No information on the chemical distribution in the test material or degradates was provided.

These studies used modified test conditions to enhance or maximize biodegradation. Under these modified test conditions, C14 41.3 wt% Cl and a C14 45.5 wt% Cl substances are readily biodegradable. More highly chlorinated and longer carbon chain CPs  (C14-17 51.7 wt% Cl, C14 55 wt% Cl, C14 60.2 wt% Cl, and C14-17  63.2 wt% Cl) biodegraded over a range of 2  -  54% in 28 days to 4  -  57% at up to 60 days. The most highly chlorinated, (C14-17   63.2 wt% Cl) biodegraded 5% in 28 days and 10% at 60 days in the enhanced biodegradation studies, suggesting that longer chain and higher chlorination can contribute to greater persistence under most environmental conditions. 
                                  Van Ginkel 
                                     2014b
                                C15 51 wt% Cl 
                             Closed bottle (301D)
                                    60 day
43% and 63% degradation at 28 and 60 days
                                  Van Ginkel 
                                     2014a
                                 C15 51wt% Cl 
                              Closed bottle (301)
                                    60 day
37% and 57% degradation at 28 and 60 days
Conclusions: Unlike the 2010 series of studies, these most recent biodegradation studies did not have significant protocol modifications and the C15 51 wt% Cl were found to be inherently degradable and possibly readily degradable in OECD 301 and 301D tests.
                              Madeley and Birtley
                                     1980
                        C14-17 mixed product, 40 wt% Cl
                                   BOD test
                                    25 days
Approximately 15.5% degradation as measured by theoretical BOD in non-acclimated samples and 22.5% degradation in acclimated samples.[1]
                              Madeley and Birtley
                                     1980
                        C14-17 mixed product, 45 wt% Cl
                                   BOD test
                                    25 days
Approximately 10% degradation as measured by theoretical BOD in non-acclimated samples and 30% degradation with acclimated soil microbes added.[1]
                              Madeley and Birtley
                                     1980
                        C14-17 mixed product, 52 wt% Cl
                                   BOD test
                                    25 days
Approximately 4% degradation as measured by theoretical BOD in non-acclimated samples and 6% degradation with acclimated soil microbes added.[1]
                              Madeley and Birtley
                                     1980
                        C14-17 mixed product, 58 wt% Cl
                                   BOD test
                                    25 days
No significant degradation
Conclusions: The data from Madeley and Birtley suggests the potential for biodegradation but has significant limitations. The BOD studies were done on mixed products. No attempt was made to determine which specific congeners were degraded or the reaction products. No identification of the congeners present was provided. The degradation was estimated from the BOD but other compounds may have contributed to the ThBOD in the bottles. BOD measurements are highly variable as evidenced by the decrease in the C20-30 42% of > 50% between day 20 and 25.

[1]The ThOD (theoretical oxygen demand) was estimated (ThOD (g O2/g substance) = 16[2xc+0.5x(h-cl)]/mw; where c=number of carbon atoms, h=number of hydrogen atoms, cl=number of chlorine atoms and MW = molecular weight). This is questionable for a product containing mixture of congeners as was used in all studies.  
                                     LCCPs
                              Madeley and Birtley
                                     1980
                        C20-30 mixed product, 42 wt% Cl
                                   BOD test
                                    25 days
Approximately 7.5% degradation as measured by theoretical BOD in non-acclimated samples and 23% degradation with acclimated soil microbes added.[1]
                              Madeley and Birtley
                                     1980
                       C25 "chlorinated pentacosane"
                            [14]C on central carbon
                                8 weeks (mean)
11% of [14]C- released as CO2. Non-acclimated microbes.
Conclusions: The data from Madeley and Birtley suggests the potential for biodegradation but has significant limitations. The BOD studies were done on mixed products. No attempt was made to determine which specific congeners were degraded or the reaction products. No identification of the congeners present was provided. The degradation was estimated from the BOD but other compounds may have contributed to the ThBOD in the bottles. BOD measurements are highly variable as evidenced by the decrease in the C20-30 42% of > 50% between day 20 and 25.

[1]The ThOD (theoretical oxygen demand) was estimated (ThOD (g O2/g substance) = 16[2xc+0.5x(h-cl)]/mw; where c=number of carbon atoms, h=number of hydrogen atoms, cl=number of chlorine atoms and MW = molecular weight). This is questionable for a product containing mixture of congeners as was used in all studies.  
                                  Hildebrecht
                                     1972
                        C20-30 mixed product, 42 wt% Cl
                                   BOD test
                                    5 days
25% degradation. Degradation was estimated by the authors as the% of the theoretical BOD based on the total carbon content of the test solution. Substances other than the chlorinated paraffin contributed to this total carbon content.
                                  Hildebrecht
                                     1972
                     > C20-30 mixed product, 70 wt% Cl
                                   BOD test
                                    5 days
2% degradation. Degradation was estimated by the authors as the% of the theoretical BOD based on the total carbon content of the test solution. Substances other than the chlorinated paraffin contributed to this total carbon content.
                                  Hildebrecht
                                     1972
                     > C20-30 mixed product, 70 wt% Cl
                                   BOD test
                                    5 days
65% degradation. Degradation was estimated by the authors as the% of the theoretical BOD based on the total carbon content of the test solution. Substances other than the chlorinated paraffin contributed to this total carbon content.
Conclusions: As described by the (EA, 2009), Hildebrecht's results are questionable (Hildebrecht, 1972). This report is not available so it cannot be reviewed directly, but others have reported that it provided limited details. A surfactant, other carbon sources, and nutrients were added that may have contributed BOD. The extent of degradation was determined by the comparing the oxygen consumption in the test with the theoretical oxygen demand (ThOD) based on oxidation to CO2 of the total organic carbon present in the solution from all sources. This estimation of ThOD does not take into account oxygen consumption by other compounds or the unknown composition. Of the CPs in the mixture, as the UK report concludes, "It is not possible to draw definite conclusions as to the degradability of the chlorinated paraffins in these tests" (EA, 2009).
                                  Hoechst AG
                                 1976 and 1977
                               C18-20, 35 wt% Cl
                                   BOD test
                                    5 days
                               0.7% degradation
                                  Hoechst AG
                                 1976 and 1977
                               C18-20, 44 wt% Cl
                                   BOD test
                                    5 days
                             < 1.2% degradation
                                  Hoechst AG
                                 1976 and 1977
                               C18-20, 49 wt% Cl
                                   BOD test
                                    5 days
                             < 2.3% degradation
                                  Hoechst AG
                                 1976 and 1977
                               C18-20, 52 wt% Cl
                                   BOD test
                                    5 days
                             < 0.6% degradation
Conclusions: The Hoechst reports from early industry studies are not available so it is not possible to directly review the data (Hoechst, 1976, 1977). Others (EA, 2009) have reported the limitations of the studies. Limited details of the studies were apparently reported by Hoechst. These tests were done on mixtures of congeners with unknown composition. They reported that the majority of the CPs were removed by sorption on to the solids so no degradation may have occurred that would have been detected as BOD. The tests were run for 5 days using non-acclimated sludge microbes so degradation may have been possible but had not yet occurred.
                                 Omori et al.
                                     1987
                         C24.5H44.5Cl6.5, 40.5 wt% Cl
                               Chloride release
                                   48 hours
9.9% degradation using bacterial strain HK-3;
13% H15-4;
2.2% HK-6;
3.5% HK-8; 
33% using mixed bacterial culture (HK-3, HK-6, HK-8 and HK-10)
                                 Omori et al.
                                     1987
                            C24.5H41Cl10, 50 wt% Cl
                               Chloride release
                                   48 hours
3% degradation using bacterial strain HK-3;
9% H15-4;
1.8% HK-6;
2.6% HK-8
                                 Omori et al.
                                     1987
                            C24.5H30Cl21, 70 wt% Cl
                               Chloride release
                                   48 hours
2.6% degradation using bacterial strain HK-3;
12% H15-4;
1.4% HK-6;
1.7% HK-8; 
15% using mixed bacterial culture (HK-3, HK-6, HK-8 and HK-10)
Conclusions: Omori et al. (1987) showed the potential for biodegradation using pure and mixed cultures in short (48 hour) incubations. No information on the starting mixtures were provided except average compositions. No data on the products were reported. Loss of Cl suggests dechlorination can occur and that lower Cl content or shorter chain lengths may be produced.
                             Allpress and Gowland
                                     1999
                               C18-20, 48 wt% Cl
                               Chloride release
                                    71 days
                11% degradation using Rhodococcus sp. bacteria
                             Allpress and Gowland
                                     1999
                              C> 20, 42 wt% Cl
                               Chloride release
                                    71 days
                14% degradation using Rhodococcus sp. bacteria
Conclusions: Allpress and Gowland (1999) also showed that CPs have the potential to biodegrade using pure culture. They used mixed congener products and did not provide any information on the composition of the starting material or the degradation products. They found that the Rhodococcus sp. was able to use CPs as carbon source as well as an energy source.
[1]The ThOD (theoretical oxygen demand) was estimated (ThOD (g O2/g substance) = 16[2xc+0.5x(h-cl)]/mw; where c=number of carbon atoms, h=number of hydrogen atoms, cl=number of chlorine atoms and MW = molecular weight). This is questionable for a product containing mixture of congeners as was used in all studies.

 BIOCONCENTRATION AND BIOACCUMULATION
EPA/OPPT's review of measured data on bioaccumulation of MCCPs are somewhat limited and conclusions vary with type of CP mixture and species evaluated (Bengtsson et al., 1979; CPC, 1980, 1983a, 1983b; Fisk et al., 1999; Fisk et al., 1998; Houde et al., 2008; Madeley and  Maddock, 1983a, 1983b; Madeley and  Thompson, 1983; Renberg et al., 1986; Thompson et al., 2000).

The limited measured data on MCCPs and LCCPs, informed by data on SCCPs, suggests that bioaccumulation is a function of chain length and degree of chlorination (see Table_Apx A-3). Some MCCP chemicals with intermediate chain length and chlorination may be absorbed and retained. The available evidence for MCCP congeners with intermediate chain lengths and chlorination suggests that some may have BCFs or BAFs greater than 1000 or 5000 (EC, 2008b; ECB, 2008). This suggests that some congeners in MCCP product mixtures may be bioaccumulative or very bioaccumulative. 

Additional evidence for bioaccumulation of MCCPs is provided by Houde et al. (2008). Field-derived log BAFs for MCCPs (C14-15), ranging from 6.5 to 7.3, were reported for several Lake Ontario aquatic species from multiple trophic levels. Canada's assessment of MCCPs also indicates that modeled BAFs for a number of MCCPs (using the Modified Gobas BAF Model with assumption of no metabolism), were all above 5000, suggesting high to very high bioaccumulation (EC, 2008a). Evidence of bioaccumulation in sediment-dwelling organisms is also provided in a study by Fisk et al. (1998). Biota-sediment accumulation factors (BASFs) ranging from 0.6 to 4.4 were reported for oligochaetes, which indicate bioaccumulation of MCCPs from sediment to biota (USEPA, 2009).

The Houde et al. (2008) study also provides evidence of biomagnification of MCCPs. BMFs derived for food chains in Lake Ontario and Lake Michigan ranged from 1 to 15. More specifically, large BMFs were observed for all MCCP chain lengths in Lake Ontario, and for C14 MCCPs in Lake Michigan, indicating biomagnification. BMFs (2.4  -  7.7) were also above 1 for smelt and lake trout in Lake Michigan. 

In laboratory studies with rainbow trout and oligochaetes, lipid-normalized equilibrium BMFs estimated from a first-order bioaccumulation model for constant dietary exposure ranged from 0.4 - 5.0 (Fisk et al., 1996; Fisk et al., 2000; Fisk et al., 1998).

Most of the laboratory-based BCF studies (Bengtsson et al., 1979; CPC, 1980, 1983a, 1983b; Fisk et al., 1999; Fisk et al., 1998; Houde et al., 2008; Madeley and  Maddock, 1983a, 1983b; Madeley and  Thompson, 1983; Renberg et al., 1986; Thompson et al., 2000), were reported to have been conducted at MCCPs concentrations above the water solubility limit and hence likely underestimate the true BCF. Furthermore, acetone was used as a solvent in these tests, so they do not adhere to OECD guidelines. Nonetheless, some BCF values estimated from these studies indicate MCCPs are bioaccumulative (e.g., bleak and rainbow trout (32-2856) and BCF of 6920 for common mussel). 

Based on these studies and estimated upper trophic level bioaccumulation factors, EPA has identified constituents including C14 51% Cl and C14 63% Cl and C18 30% Cl through C18 70% Cl as potentially bioaccumulative or very bioaccumulative. Further discussion of these findings can be found in Table _Apx A-3: Review of MCCP and LCCP Bioaccumulation Studies and Table_Apx A-4: Estimated BCF/BAF Values for MCCP and LCCP Constituents C14-C20 30 - 70 wt % Cl.

Table_Apx A-3: Review of MCCP and LCCP Bioaccumulation Studies

Conclusion for Table_Apx A-3: Based on these studies, EPA has identified constituents including C14 51% Cl and C14 63% Cl as potentially bioaccumulative or very bioaccumulative.

Table_Apx A-3: Bioaccumulation studies on MCCPs (C14-17) and LCCPs (> C18) 
                                     MCCPs
                                 Study Authors
                               Publication Date
              MCCP/LCCP Chemicals Evaluated (i.e., C-length,% Cl)
                                    Method
                                Study Duration
                      Noteworthy Results and Implications
Houde et al.
2008
C14-15 Only
BAF = ([predator]/[water (filtered)]);

BMF) = [predator]/[prey]) where the concentrations in predator and prey are on a lipid basis
Three sampling periods: October 2000, June 2002, and
July 2004.
Issues related to the temporal variability of water concentrations over the period of biota sampling (1999  -  2004) in this study have been raised (ECB, 2005; EC, 2008) contributing to uncertainties associated with the reported BAF values.

Log BAF = 
Plankton: C14=6.2; C15=6.6; ∑=6.5
Alewife: C14=7.0; C15=6.8; ∑=6.9
Sculpin: C14=7.4; C15=7.2; ∑=7.3
Rainbow smelt: C14=7.4; C15=7.1; ∑=7.2
Lake trout: C14=6.8; C15=6.5; ∑=6.6

BMF (Lake Ontario) =
0.25 (lake trout  -  alewife);
0.14  (lake trout  -  smelt);
8.7 (sculpin  - Diporeia)

BMF (Lake Michigan) = 
0.22 (lake trout  -  alewife); 
0.94 (lake trout  -  sculpin);
0.88 (sculpin  -  Diporeia)
Thompson et al.; as summarized in ECB, 2005
2000
n-pentadecane-8-[14]C, 51% Cl mixed with a non-radio-labelled C14-17, 51% Cl chlorinated paraffin
Freshwater; flow-through; acetone solvent used;
35 days
Steady-state may not have been achieved, so kinetic BCF data considered more reliable. 

BCF = 860 L/kg at 35 days when exposed at 0.9 ug/L
BCF = 265 L/kg at 35 days when exposed at 4.9 ug/L
kinetic BCF = 1,087 L/kg at 35 days when exposed at 0.9 ug/L
kinetic BCF = 349 L/kg at 35 days when exposed at 4.9 ug/L
CPC (Madeley et al.); as  summarized in ECB, 2005
1983
commercial product mixed with a n-pentadecane-8-[14]C chlorinated to a similar degree
freshwater; flow-through; rainbow trout; acetone solvent used
60 days
Concentrations above water solubility; hence, water concentrations may be overestimated and BCF underestimated. 
Uncertainty as to whether steady-state was reached.

BCF = 32-45 l/kg on a wet weight basis when exposed at 1.05 mg/l;  
BCF = 42-67 l/kg on a wet weight basis when exposed at the 4.5 mg/l
CPC (Madeley and Pearson); as summarized in ECB, 2005
1980
C14-17, 45% Cl
freshwater; flow-through; rainbow trout; 
28 days
Measured water concentrations questionable; water concentrations may be overestimated and BCF underestimated. 

BCF = 50-60 l/kg based on nominal exposure concentrations
BCF = 280-600 l/kg based on measured water concentrations
Madeley and Maddock; as summarized in ECB, 2005
1983
Total  MCCPs
Bioconcentration factors. MCCPs concentrations were above the water solubility limit, using acetone as the co-solvent in the test solutions, and hence are not in compliance with OECD guideline requirements
No Information
BCF = 32  -  2856 for common mussel, bleak and rainbow trout. May not have reached steady-state.
Fisk et al.

1999
Average formula: C14H23.3Cl6.7, 55% Cl
freshwater; medaka eggs
20-days
Uncertainty as to whether steady-state was reached; hence BCFs probably represent lower limit of true value

BCF = 32- 680 L/kg 
Fisk et al.
1998
[14]C16  35% Cl and [14]C16  69% Cl
Lake sediments were spiked and worms added after 18 and 32
No Information
Kinetic BAF probably represents the
upper limit of the true bioaccumulation factor

[14]C16  35% Cl
14-day BSAFss = 0.7
Kinetic BSAF = 4.4

[14]C16  69% Cl 
14-day BSAFss = 0.2
Kinetic BSAF = 0.6

Bengtsson et al.

1979
C14-17, 50% Cl
seawater; semi-static; bleak;
acetone solvent used
14 days
Measured water concentrations questionable; water concentrations may be overestimated and BCF underestimated. 

BCF  40 L/kg
Madeley and Thompson; as summarized in ECB, 2005
1983
commercial C14-17, 52% Cl
seawater; flow-through; mussel
acetone solvent used
60 days
BCFs = 2,182 L/kg (parent compound analysis) or 2,856 L/kg ([14]C-measurements) when exposed to 0.22 mg/l

BCF = 339 L/kg (parent compound analysis) or 429 l/kg ([14]C measurements)
when exposed to 3.8 mg/l.
Renberg et al.
1985
C16H30.7Cl3.3 (34% Cl) and C12H16Cl9.8 (68.5% Cl) mixture synthesized with [14]C radiolabel
Flow through exposure to mussel (Mytilus edulis)
C16 - 0.13 and 5.0 ug/L
C16 - 28 day uptake
C12 - 21 day uptake followed by 28 day depuration
Steady state BCF about 7000 for C16 and 140,000 for C12 based on 14C quantification.
No chemical specific analysis for CPs. Metabolism and accumulation of degradation products may have accounted for high values.
                                     LCCPs
Bengtsson et al.; as summarized in ECB, 2005

1979
C18 - 26
concentrations were above the water solubility limit and hence are not in compliance with OECD guideline requirements
No Information
Concentrations above water solubility; hence, water concentrations may be overestimated and BCF underestimated. Uncertainty as to whether steady-state was reached.

BCF reported  = 8  -  16 L/kg

Table_Apx A-4: Estimated BCF/BAF Values for MCCP and LCCP Constituents 
 
Very limited data were found on BCF/BAF for MCCPs and LCCPs. To supplement available data EPA estimated BCFs and BAFs for individual constituents of the MCCPs using the Arnot-Gobas BCF and BAF model in EPISuite. The Arnot-Gobas model estimates steady-state bioconcentration factor (BCF; L/kg) and bioaccumulation factor (BAF; L/kg) values for non-ionic organic chemicals in three general trophic levels of fish (i.e., lower, middle and upper) in temperate environments. The model calculations represent general trophic levels (i.e., not for a particular fish species) and are derived for "representative" environmental conditions (e.g., dissolved and particulate organic carbon content in the water column, water temperature). Thus, it provides general estimates for these conditions in absence of site-specific measurements or estimates. The model includes mechanistic processes for bioconcentration and bioaccumulation such as chemical uptake from the water at the gill surface (BCFs and BAFs) and the diet (BAFs only), and chemical elimination at the gill surface, fecal egestion, growth dilution and metabolic biotransformation. Other processes included in the calculations are bioavailability in the water column (only the freely dissolved fraction can bioconcentrate) and absorption efficiencies at the gill and in the gastrointestinal tract. The model requires the octanol-water partition coefficient (KOW) of the chemical and the normalized whole-body metabolic biotransformation rate constant (kM, N; /day) as input parameters to predict BCF and BAF values. The required kM, N value must be normalized to a fish of 10 g. 

Table_Apx A-4: Estimated BCF/BAF Values for MCCP and LCCP Constituents C14-C20 30 - 70 wt % Cl[1]

                                    Formula
                                    Log BCF
                                   Log P (E)
                                 t 1/2 (days)
                                   Log BAF 
                                    SMILES
                                     % Cl

                                   Upper TL
                                   Middle TL
                                   Lower TL

C14Cl2
3.2
7.6
15
5.0
5.1
5.3
CC(Cl)CCCCCCCCCC(Cl)CC
27
C14Cl3
3.2
7.8
20
5.2
5.2
5.3
CC(Cl)CCCCC(Cl)CCCCC(Cl)CC
35
C14Cl4
3.1
7.9
27
5.4
5.4
5.4
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CCCCCC
42
C14Cl5
3.0
8.1
33
5.4
5.4
5.4
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CCC(Cl)CCC
48
C14Cl6
3.5
8.3
46
5.6
5.5
5.4
CC(Cl)CC(Cl)C(Cl)CC(Cl)C(Cl)CC(Cl)CCCC
53
C14Cl7
3.4
8.5
55
5.6
5.4
5.3
CC(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)CC(Cl)CC
56
C14Cl8
3.3
8.7
71
5.6
5.4
5.3
CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)CC
60
C14Cl9
3.2
8.8
92
5.6
5.4
5.2
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)CC
63
C14Cl10
3.1
9.0
120
5.6
5.4
5.2
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
65
C14Cl11
3.0
9.2
155
5.6
5.3
5.1
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
68
C14Cl12
2.9
9.5
209
5.5
5.2
5.0
C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
70
C15Cl3
2.9
8.3
27
5.2
5.2
5.2
CCC(Cl)CCCCCC(Cl)CCC(Cl)CCC
34
C15Cl4
2.8
8.4
35
5.2
5.2
5.2
CCC(Cl)CC(Cl)CCCC(Cl)CCC(Cl)CCC
40
C15Cl5
2.7
8.7
47
5.3
5.2
5.1
C(Cl)CC(Cl)CC(Cl)CCCC(Cl)CCC(Cl)CCC
46
C15Cl6
2.7
8.8
58
5.4
5.2
5.1
CCC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC
51
C15Cl7
3.2
9.0
76
5.4
5.2
5.0
CCC(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)CC(Cl)CC
55
C15Cl8
3.1
9.2
98
5.4
5.1
5.0
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
58
C15Cl9
3.0
9.3
127
5.4
5.1
4.9
CC(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
61
C15Cl10
2.9
9.5
165
5.3
5.0
4.8
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
64
C15Cl11
2.8
9.7
213
5.3
5.0
4.7
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
66
C15Cl12
2.7
9.9
276
5.2
4.9
4.6
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
68
C15Cl13
2.6
10.1
>1yr
5.1
4.7
4.5
C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
70
C16Cl3
2.7
8.7
40
5.1
5.0
5.0
CC(Cl)CCCCCC(Cl)CCCC(Cl)CCCC
32
C16Cl4
2.6
8.9
52
5.2
5.0
4.9
CC(Cl)CCC(Cl)CCC(Cl)CCCC(Cl)CCCC
39
C16Cl5
2.5
9.1
62
5.1
4.9
4.8
CC(Cl)CCC(Cl)CCC(Cl)CCCC(Cl)CC(Cl)CC
44
C16Cl6
2.4
9.3
87
5.2
5.0
4.8
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)CCCC
49
C16Cl7
2.3
9.5
104
5.11
4.9
4.7
CC(Cl)CC(Cl)CC(Cl)CCC(Cl)C(Cl)CC(Cl)C(Cl)CCC
53
C16Cl8
2.8
9.6
135
5.1
4.8
4.6
CC(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)CCC(Cl)CC(Cl)CC(Cl)CC
56
C16Cl9
2.7
9.8
175
5.1
4.8
4.5
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CCC(Cl)CC(Cl)CC(Cl)CC
59
C16Cl10
3.0
9.3
127
5.4
5.1
4.9
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CCC(Cl)C(Cl)CC(Cl)CC
62
C16Cl11
2.6
10.2
294
4.9
4.6
4.4
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CCC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
64
C16Cl12
2.5
10.4
>1yr
4.8
4.5
4.2
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)CC
66
C16Cl13
2.4
10.6
>1yr
4.7
4.4
4.1
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
68
C16Cl14
2.3
10.8
>1yr
4.6
4.2
3.9
C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C
70
C17Cl3
2.4
9.2
51
4.8
4.7
4.6
CC(Cl)CCCCCCCC(Cl)CCCC(Cl)CCC
31
C17Cl4
2.4
9.4
66
4.9
4.7
4.6
CCC(Cl)CCCC(Cl)CCCCC(Cl)CC(Cl)CCC
37
C17Cl5
2.3
9.6
86
4.9
4.6
4.5
CC(Cl)CC(Cl)CCCC(Cl)CCCC(Cl)CCC(Cl)CC
43
C17Cl6
2.2
9.8
111
4.9
4.6
4.4
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CCCC(Cl)CCC(Cl)CC
48
C17Cl7
2.1
10.0
144
4.8
4.5
4.4
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CCC(Cl)CC(Cl)CC(Cl)CC
52
C17Cl8
2.0
10.1
186
4.8
4.5
4.3
CC(Cl)CC(Cl)CC(Cl)CCC(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)CC
55
C17Cl9
2.5
10.3
241
4.7
4.4
4.2
CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
58
C17Cl10
2.4
10.5
313
4.6
4.3
4.1
CC(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
61
C17Cl11
2.3
10.7
>1yr
4.5
4.2
3.9
CC(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC
63
C17Cl12
2.2
10.9
>1yr
4.4
4.1
3.8
CC(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
65
C17Cl13
2.2
11.0
>1yr
4.3
4.0
3.7
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
67
C17Cl14
2.1
11.2
>1yr
4.2
3.8
3.6
CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
69
C17Cl15
1.9
11.5
>1yr
4.0
3.6
3.4
C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
70
C18Cl3
2.2
9.7
76
4.7
4.5
4.3
CC(Cl)CCCCCCC(Cl)CCCC(Cl)CCCCC
 30 
C18Cl4
2.1
9.9
99
4.7
4.4
4.2
CC(Cl)CC(Cl)CCCCC(Cl)CCC(Cl)CCCCCC
 36 
C18Cl5
2.0
10.1
118
4.6
4.3
4.1
CC(Cl)CC(Cl)CC(Cl)CCCCCC(Cl)CCCC(Cl)CC
 42 
C18Cl6
1.9
10.3
153
4.6
4.3
4.1
CC(Cl)CC(Cl)CCC(Cl)CC(Cl)CCCC(Cl)CC(Cl)CCC
 46 
C18Cl7
1.8
10.4
198
4.5
4.2
4.0
CC(Cl)CC(Cl)CC(Cl)CCC(Cl)CCC(Cl)CC(Cl)CC(Cl)CC
 50 
C18Cl8
1.8
10.6
257
4.4
4.1
3.9
CC(Cl)CC(Cl)CC(Cl)CCCC(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)CC
 54 
C18Cl9
1.7
10.8
332
4.4
4.0
3.8
CC(Cl)CC(Cl)CC(Cl)CC(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)CC(Cl)CC
 57 
C18Cl10
2.2
11.0
>1yr
4.3
3.9
3.7
CC(Cl)CC(Cl)CC(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)CC
 59 
C18Cl11
2.1
11.2
>1yr
4.2
3.8
3.5
CC(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)CC(Cl)CC
 62 
C18Cl12
2.0
11.4
>1yr
4.0
3.6
3.3
C(Cl)C(Cl)CC(Cl)CC(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)CC
 64 
C18Cl13
1.9
11.6
>1yr
3.8
3.5
3.2
C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
 66 
C18Cl14
1.8
11.8
>1yr
3.7
3.3
3.1
C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
 67 
C18Cl15
1.7
12.0
>1yr
3.5
3.2
2.9
C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC
 69 
C18Cl16
1.6
12.1
>1yr
3.4
3.0
2.8
C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)CC(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C(Cl)C
 70 
C19Cl3
2.0
9.7
76
4.7
4.5
4.3
CC(Cl)CCCCCCC(Cl)CCCC(Cl)CCCCC
 30 
C19Cl4
1.8
9.9
99
4.7
4.4
4.2
CC(Cl)CC(Cl)CCCCC(Cl)CCC(Cl)CCCCCC
 36 
C18Cl5
1.8
10.1
118
4.6
4.3
4.1
CC(Cl)CC(Cl)CC(Cl)CCCCCC(Cl)CCCC(Cl)CC
 42 
C19Cl5
1.8
10.6
176
4.3
4.0
3.8
CC(Cl)CCCC(Cl)CC(Cl)CC(Cl)CCCC(Cl)CCCCC

C19Cl6
1.7
10.8
237
4.2
3.9
3.6
C(Cl)C(Cl)CCCC(Cl)CC(Cl)CC(Cl)CCCC(Cl)CCCCC
 46 
C19Cl7
1.6
10.9
273
4.2
3.8
3.6
CC(Cl)CC(Cl)CC(Cl)CCCC(Cl)CCC(Cl)CC(Cl)CC(Cl)CC
 50 
C19Cl8
1.5
11.1
>1yr
4.1
3.7
3.5
CC(Cl)CC(Cl)CC(Cl)CCC(Cl)CCCC(Cl)CC(Cl)C(Cl)C(Cl)CC
 54 
C20Cl5
1.5
11.1
242
4.0
3.6
3.4
CC(Cl)CCCC(Cl)CC(Cl)CC(Cl)CCCCC(Cl)CCCCC
 42 
C20Cl6
1.4
11.3
326
3.8
3.5
3.2
C(Cl)C(Cl)CCCC(Cl)CC(Cl)CC(Cl)CCCCC(Cl)CCCCC
 46 
C20Cl7
1.4
11.4
>1yr
3.8
3.4
3.2
CC(Cl)CC(Cl)CC(Cl)CCCCC(Cl)CCC(Cl)CC(Cl)CC(Cl)CC
 50 
C20Cl8
1.3
11.6
>1yr
3.7
3.3
3.1
CC(Cl)CC(Cl)CC(Cl)CCC(Cl)CCCCC(Cl)CC(Cl)C(Cl)C(Cl)CC
 54 

[1] USEPA 2012 Estimation Programs Interface Suite (TM) Version 4.11 BCF/BAF V 3.01

 ECOTOXICITY STUDY SUMMARIES

 MCCP ECOTOXICITY DATA
 Acute Fish Toxicity
(1) A series of 96-hour acute fish toxicity studies were conducted by Mayer an Ellersieck (1986) with Paroil 1048 (50-52% Cl, C15H26Cl6) similarly to ASTM (1980). Bluegill sunfish (Lepomis macrochirus) and yellow perch (Perca flavescens) were exposed to the test substance in a flow-through test system and channel catfish (Ictalurus punctatus) and rainbow trout (Oncorhynchus mykiss) were exposed to the test substance in a static test system. Solvent use was not specified for this compound. The average pH level was between 7.4 and 7.5 for all tests. Test temperature was 12 ºC for bluegill sunfish, rainbow trout, and yellow perch and 20 ºC for channel catfish. Dilution water hardness was 44 mg CaCO3/L in the rainbow trout and channel catfish test system and 314 mg CaCO3/L for the bluegill sunfish and yellow perch test system. Reported effect levels are considered to be nominal with LC50 values of >10 mg/L for bluegill sunfish, channel catfish, and yellow perch and >0.011 mg/L for rainbow trout; all values are greatly above the limit of solubility. 

                  EPA/OPPT Conclusion
                  Using a weight-of-evidence approach, these studies were considered acceptable to characterize the acute fish toxicity endpoint.
                  96-hr LC50 = NES

(2) A 96-hour acute fish toxicity study was published by Linden et al. (1979). Groups of 10 Bleak (Alburnus alburnus) were exposed to six nominal unspecified concentrations of Cereclor S52[(R)]  (C14-17, 52% Cl), Chloroparaffin huls 40G (C15.5, 40% Cl), and Witaclor 50 (C14-17, 50% Cl) under static test conditions. Salinity was 7 ppt, pH was 7.8, temperature was 10 ºC, and dissolve oxygen was considered by study authors to be satisfactory. EPA/OPPT requires reporting of dissolved oxygen concentrations to determine study adequacy. EPA/OPPT also does not consider the test species, the bleak, a standard test species. The 96-hour fish LC50 values were >10,000 mg/L, >5,000, and >5,000 for Cereclor S52[(R)], Chloroparaffin huls 40G, and Witaclor 50. 

                  EPA/OPPT Conclusion
                  Given effect levels observed in Mayer and Ellersieck (1986) and the reported water solubility of medium chain paraffins, these studies were considered acceptable using a weight-of-evidence approach to characterize the acute saltwater fish toxicity endpoint.
                  96-hr LC50 = NES

(3) Bengtsson et al. (1979) also studied the toxicity of a medium-chain chlorinated paraffin to Bleak (Alburnus alburnus) as part of a bioaccumulation study. The chlorinated paraffin tested was a C14-17, 50% wt. Cl substance. The tests were performed at 10 °C using a semi-static procedure in which the test solutions containing 125 μg/L of the substance were renewed every two to three days over the 14-day exposure period. The water used in the experiment was Baltic Sea water with a salinity of 7%., and acetone was present in all aquaria, including controls at a concentration of 0.1 ml/l. The fish used in the experiment had an average weight of 4.5 g and were not fed during the exposure period. Six groups of 15 fish were used for both the exposure and control solutions. No mortality or effect on behavior was seen in fish exposed to the medium-chain chlorinated paraffin during the test. 

                  EPA/OPPT Conclusion
                  This data review was part of a BAF study and as such will be used as a weight of evidence to support other data for this category of organisms.

 Acute Aquatic Invertebrate Toxicity
(1) A 48-hour acute Daphnia magna toxicity study was conducted by Thompson et al. (1996) according to OECD TG 202 (1984) with GLP compliance using a static test system. The test substance was identified as Cereclor S52[(R)], a C14-17 chlorinated paraffin with 52% chlorination that contained 0.3% epoxy soya bean oil stabilizer as well as a small amount of radiolabelled n-pentadecane-8-[14]C (51% chlorinated). Four replicates of 5 Daphnia magna Straus (<24 hours old) were exposed to nominal concentrations of 0 (dilution water control), 0 (solvent control), 0.0032, 0.0056, 0.01, 0.018, 0.032, 0.056, and 0.1 mg/L test substance in acetone (0.1 mL/L). Test solutions were prepared by adding the appropriate stock solution to dilution water while continuously and vigorously stirring with a magnetic follower. Appearance of test solutions was not provided. Corresponding mean measured concentrations determined by radiochemical methods were 0.0025, 0.0041, 0.0094, 0.015, 0.024, 0.047, and 0.095 mg/L. Daphnid loading was 25 daphnids/L. Over the course of the study dissolved oxygen concentrations remained between 9 and 9.2 mg/L, pH remained within 8 and 8.1, and temperatures were 20 +-1 ºC. Dilution water had a total water hardness of 248 mg CaCO3/L. At 48 hours, 0%, 45%, 90%, 75%, 85%, 100%, and 100% immobilization was observed at the mean measured concentrations of 0.0025, 0.0041, 0.0094, 0.015, 0.024, 0.047, and 0.095 mg/L, respectively. Red coloration on parts of the exoskeleton was observed in animals exposed to each of the test substance treatments, which the laboratory notes as being of an uncertain significance. 

                  EPA/OPPT Conclusion
                  The study is acceptable.
                  48-hr EC50 = 0.0059 mg/L

(2) A 48-hour acute Daphnia magna toxicity study was conducted the University of Bremen, Department of Physical and Environmental Chemistry with CP 52 (C12-18, 52% chlorination) according to DIN 38412 by Koh and Thiemann (2001). Study methods were not fully characterized. Additional communications with the study author Wolfram Thiemann clarified that a static test system was used with nominal test concentrations. Based on communications with the study author, local (Bremen, Germany) tap water was used without adjustments. Presumed pH was between 5 and 6 and water hardness was between 35.7 and 53.5 mg CaCO3/L. Ambient laboratory air temperature was around 21 ºC. The solvent acetone was used to maintain test substance in solution. Floating effects at the surface of the water were observed in individual cases due to undissolved oil slicks, but communications with the study author noted that there was no significant loss of daphnids due to mechanical trapping since most daphnid swam away from these occasional slicks observed at the higher test concentrations. 
                  
                  EPA/OPPT Conclusion
                  This study is considered acceptable. 
                  48-hr EC50 = 0.052 mg/L

(3) A 48-hour acute Daphnia magna toxicity study was conducted by Thompson et al. (1994) according to OECD TG 202 (1984) with GLP compliance using a static test system. The test substance was identified as Cereclor S52[(R)], a C14-17 chlorinated paraffin with 52% chlorination that was mixed with an equal weight of radiolabeled n-pentadecane-8-[14]C (51% chlorinated). Four replicates of 5 Daphnia magna (<24 hours old) were exposed to 0% (dilution water control), 6.3%, 12.5%, 25%, 50%, and 100% of stock solution containing test substance. The test substance was prepared in solution by (1) combining 0.75 g test substance and 25 mL acetone to a borosilicate glass conical flask, (2) evaporation of the acetone using a stream of nitrogen, (3) addition of 1.5 L dilution water, (4) stirring for three days, and (5) filtration of the aqueous phase. Radiochemical methods were used to determine the concentration of test substance in solution. Nominal concentrations of 0 (dilution water control), 0.14, 0.28, 0.55, 1.1, and 2.2 mg/L were within 86-100% of measured concentrations. Concerns regarding test solution preparation methods and analytical technique were identified by the submitter that included increasing the level of more soluble impurities (i.e., short chain chlorinated paraffins), questionable analytical monitoring results due to the presence of radio-labeled impurities, and abnormally low recovery of the chlorinated paraffin into hexane. Over the course of the study dissolved oxygen concentrations remained between 8 and 9 mg/L, pH remained within 8 and 8.1, and temperatures were 20 +-1 ºC. Dilution water had a total water hardness of 237 mg CaCO3/L. Observed immobilization was limited to the highest test concentration (100% solution) with 55% immobilization. 

                  EPA/OPPT Conclusion
                  The study is unacceptable since EPA/OPPT agrees that methods used to prepare the test solution and analyze the test concentrations were questionable.

4) The following study summary (Frank, 1993; Frank and Steinhäuser, 1994) provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was considered supportive of the aquatic invertebrate hazard determination. The chlorinated paraffin used in these studies was a commercial C14-17 product with a 52% by weight chlorine content. Daphnia magna were exposed to nominal concentrations of either 100 mg/L or 10,000 mg/L. The 100 mg/L solution was sonicated for 1 hour and then left to stand in the dark for 48 hours before use. The 10,000 mg/L solution also stood for 48 hours in the dark before use, but this time without sonication. After this period, both solutions were filtered firstly with glass filters and then with membrane filters to remove undissolved test substance. The concentrations of medium-chain chlorinated paraffin in the water soluble fractions were then determined by AOX (adsorbable organic halogen) analysis (detection limit of 10 μg/L Cl was equivalent to around 20 μg/L of the chlorinated paraffin). This analysis showed that the concentration of chlorinated paraffin present in the water soluble fraction was around 0.404-0.500 mg/L for the 10,000 mg/L nominal solution and 0.071-0.142 mg/L L for the 100 mg/L stock solution. The acute (48-hour) toxicity tests were carried out using dilutions of the two prepared water soluble fractions. The method used was DIN 38 412, Teil 11, which is equivalent to OECD 202. 

In the tests using the water soluble fraction from the 100 mg/L nominal solutions no toxicity was seen at concentrations up to the undiluted stock solution (i.e. no effects up to around 0.071-0.142 mg/L). In experiments using the water soluble fraction from the 10,000 mg/L stock solution, an EC0 of 0.140 mg/L (also reported as 0.100-0.110 mg/L in the paper) and an EC25 of 0.423 mg/L (also reported as 0.420-0.470 mg/L in the paper) was determined (maximum mortality seen was 25%) (Frank, 1993). The latter results for the 10,000 mg/L stock solution were reported by Frank and Steinhäuser (1994) as EC0 = 0.140 mg/L and EC25 = 0.339 mg/L, and it was noted that some of the Daphnia were floating on the surface of the test solution. In the later study (Frank and Steinhäuser, 1994), the results of further acute toxicity studies were reported using the same test method. An EC50 of 0.037 mg/L and an EC0 of 0.009 mg/L were determined using the water soluble fraction from the 100 mg/L stock solution and no toxic effects were seen in tests with the water soluble fraction from the 10,000 mg/L stock solution (approximately EC0 >=0.525 mg/L). The authors noted that the effects seen in the acute tests showed poor reproducibility, probably because effects were seen only around the water solubility limit of the substance. However, the authors thought that the possibility of undissolved droplets affecting the results could be ruled out, as floating Daphnia were only sporadically observed in the test.
                  
                  EPA/OPPT Conclusion
                  Tthe results of these studies should be treated with caution, as the effects were mainly seen in the saturated solutions only.
                  48-hour EC50 = 0.037 mg/L; 100 mg/L stock  (Frank and Steinhäuser, 1994)

5) The following study summary (Thompson and Gore, 1999) provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was considered supportive of the aquatic invertebrate hazard determination. The acute toxicity of C14-17, 52% wt. Cl substance was tested using the freshwater crustacean Gammarus pulex and the freshwater daphnid, Daphnia magna. The medium-chain chlorinated paraffin used was dissolved in acetone and then added to beakers in two separate studies containing either Gammarus or D. magna to give nominal concentrations of 0.1, 0.32, and 1.0 mg/L. A control and solvent control (containing 0.1 mL/L acetone) were also run. The tests were carried out for 96 hours at 15 ºC, with the solutions being renewed after 48 hours. The water used in the study had a hardness of 220 mg/L as CaCO3 and had a pH of 8.0-9.2. No mortalities of the Gammarus were seen in any of the test substance solutions or control. One animal died in the solvent control. Therefore, no significant toxic effects were seen with the medium-chain chlorinated paraffin over the concentration range tested. This contrasted markedly to the situation when Daphnia magna were exposed using the same test system at 20 ºC over 48 hours, where complete immobilization was seen at the lowest test concentration (0.1 mg/L).

                  EPA/OPPT Conclusion
                  The high immobilization rate observed in Daphnia magna in this study appears consistent with the other studies and Gammarus pulex appear to be a less sensitive to medium chained chlorinated paraffins then Daphnia magna. EPA/OPPT reserves judgment on the acceptability of this study until further details become available.
                  96-hr EC50 (Gammarus pulex) > 1 mg/L
                  48-hr EC50 (Daphnia magna) < 0.1 mg/L

6) The following study summary (Tarkpea et al., 1981; as quoted in WHO, 1996) provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was considered supportive of the aquatic invertebrate hazard determination. The results of tests with the brackish water harpacticoid Nitocra spinipes have been reported (Tarkpea et al., 1981). No other details of the test were reported but the test method was probably the same as reported by Tarkpea et al. (1986), where a static method was employed using water of salinity 7%. at a temperature of 20-22 ºC without aeration, probably using acetone as cosolvent. 

                  EPA/OPPT Conclusion
                  The results are considered supportive to address aquatic invertebrate acute toxicity. 
                  96-hour LC50 = 9 mg/L (C14-17, 45% wt Cl)
                  96-hour LC50 >10,000 mg/L (C14-17, 52% wt. Cl)

 Algae Toxicity
(1) A 72-hour algae toxicity study was conducted by the University of Bremen, Department of Physical and Environmental Chemistry with CP 52 (C12-18, 52% chlorination) according to DIN 38412 by Koh and Thiemann (2001). Study methods were not fully characterized. Additional communications with the study author Wolfram Thiemann clarified that a static test system was used with nominal test concentrations. Scenedesmus subspicatus were exposed to the test substance and cell density was determined using a particle counter. Based on communications with the study author, local (Bremen, Germany) tap water was used without adjustments. Presumed pH was between 5 and 6 and water hardness was between 35.7 and 53.5 mg CaCO3/L. Ambient laboratory air temperature was around 21 ºC. The solvent acetone was used to maintain test substance in solution. Effects were calculated based on growth rate. No effects were observed up to 0.1 mg/L. 
                  
                  EPA/OPPT Conclusion
                  Due to deficiencies/missing details in the study methods, the study alone was not acceptable to characterize aquatic toxicity to plants.
                  72-hr NOEC = 0.1 mg/L (Highest Test Concentration)
                  
(2) A 96-hour algae toxicity study was conducted according to OECD TG 201 (2006). The test substance was a commercial product of a C14-17 chlorinated paraffin with 52% chlorination that contained 0.3% epoxy soya bean oil stabilizer as well as a small amount of radiolabeled n-pentadecane-8-[14]C (51% chlorinated). Selenastrum capricornutum were exposed to nominal concentrations of 0 (dilution water control), 0 (solvent control), 0.1, 0.18, 0.32, 0.56, 1, 1.8, and 3.2 mg/L test substance in the solvent acetone. Six replicates were tested for each control and three replicates were tested for each treatment. A mean measured concentration of 0.49, 0.77, and 1.2 mg/L was determined using radiochemical analysis for the nominal concentrations of 1, 1.8, and 3.2 mg/L, respectively, but effects were reported based on nominal test concentrations. At the start of the test, the pH was 7.4-7.5, but had reached 10.0-10.3 by the end of the test. The shift in pH was thought to be a function of the high control growth rates observed in the test according to the study summary. The section-by-section coefficient of variation for the solvent control remained below 35% indicating acceptable control growth rates throughout the duration of the study. 

                  EPA/OPPT Conclusion
                  The maximum inhibition in the growth rate and biomass seen was 3% and 18%, respectively, but a dose response relationship was not seen. The nominal NOEC was 0.1 mg/L and the nominal LOEC based on 18% biomass inhibition was 0.18 mg/L. A GMATC of 0.134 mg/L was calculated. The study was considered acceptable.
                  72-hour EC50 = >3.2 mg/L (nominal); 1.2 mg/L (mean measured).
                  96-hour EC50 = >3.2 mg/L (nominal); 1.2 mg/L (mean measured).
                  72-hr NOECb = 0.1 mg/L 
                  72-hr LOECb = 0.18 mg/L 
                  72-hr GMATC = 0.134 mg/L 
 Chronic Fish Toxicity
(1) A 60-day fish toxicity study was conducted by Brixham Laboratories in 1983 with radio-labeled chlorinated (52%) n-pentadecane (Trade Name: Cereclor S52[(R)] ) under flow through testing conditions. A full non-CBI study report was submitted under TSCA in 1983 as DCN 40-8332184 (OTS Fiche 0507258). Two replicates of 3 immature rainbow trout (Salmo gairdneri) per concentration were exposed to nominal concentrations of 0 (dilution water control), 0 (acetone control, 500 ppm), 1, or 5.6 mg/L in 500 ppm acetone. Corresponding mean measured concentrations were 0, 0, 1.05, and 4.5 mg/L. Test concentrations were determined by radio activity measurements. Flow rate of the test system was 0.25 mL/minute for exposure concentrations. No mortality or adverse sub-lethal behavioral effects were observed for the duration of the 60-day exposure period. Effects observed were limited to the highest test concentration and involved sluggish movements. The measured NOEC was identified as 4.5 mg/L. In addition to the hazard assessment, the submitter provided an assessment of bioconcentration which indicated that analytically determined exposure concentrations of 1.05 and 4.5 mg/L resulted in fish tissue concentrations of 34 and 190 ug/g wet weight, respectively.

                  EPA/OPPT Conclusion
                  This study appears to have been previously reviewed by EPA in 1985. The previous conclusion that "a fish full life cycle toxicity test or modification thereof is needed to address the effects of CPs present in fish eggs during embryonic development" (U.S. EPA Memorandum, 1991) is still relevant for MCCPs. Thus, this study is considered unacceptable to characterize chronic population-level effects in fish. 
                  60-day NOEC = 4.5 mg/L
                  
(2) A 28-day fish toxicity study was conducted by Brixham Laboratories in 1978 with a C14-17 chlorinated paraffin having 45% chlorination under unspecified testing conditions. The study report was submitted under TSCA in 1992 as DCN 88920006972 (OTS Fiche 0545375). Rainbow trout (Salmo gairdneri) per concentration were exposed to nominal concentrations of 0 (dilution water control), 0.1, or 1 mg/L in acetone. The age and size of the rainbow trout used in the study were not specified in the study. The specific environmental conditions of the test, such as pH, temperature and water quality were not specified in the report. Concentrations of the chlorinated paraffin in the test water were measured using TLC analytical procedures resulting in mean measured concentrations of 0.01 and 0.18 mg/L. Mortality and behavior (response to food, general behavior, swimming behavior and pigmentation) were assessed during the 28-day study. Survival was 96.6 and 100% for the mean measured exposures of 0.01 and 0.18. No behavioral effects were seen over the course of the study. 

                  EPA/OPPT Conclusion
                  The study was considered unacceptable to characterize the chronic fish toxicity endpoint since insufficient study details were provided including the age and/or the life-stages of the exposed organisms.

(3) A 20-day Japanese medaka (Oryzias latipes) embryo toxicity study was conducted with the formulation C14H24.9Cl5.1, 48%Cl (composition: 10.5% 1, 2, 13, 14-tetrachlorotetradecane (42.3% Cl); 74.3% x, 1, 2, 13, 14-pentachlorotetradecane (47.7% Cl); 14.2% x, y, 1, 2, 13, 13-hexachlorotetradecane (52.6% Cl); 1.0% x, y, z, 1, 2, 13, 14-heptachlorotetradecane (56.4% Cl)) by Fisk et al. (1999) under static testing conditions. Five sets of 10 vials containing 1 egg each were exposed to nominal concentrations of 0.001, 0.010, 0.100, 1, or 10 mg/L test substance starting after fertilization and terminating approximately 3 days post-hatch. No adverse effects were reported in exposed embryos. 
                  
                  EPA/OPPT Conclusion
                  The study was considered unacceptable primarily due to insufficient exposure duration and insufficient number of eggs per exposure concentration.

(4) A 20-day Japanese medaka (Oryzias latipes) embryo toxicity study was conducted with the formulation [14]C-C14H23.3Cl6.7, 55% Cl (composition: 0.2% C14H26Cl4 (42.3% Cl), 4.4% C14H25Cl5 (47.7% Cl), 34% C14H24Cl6 (52.6% Cl), 45% C14H23Cl7 (56.4% Cl), 14% C14H22Cl8 (59.9% Cl), and 1.9% C14H21Cl9 (62.8% Cl)) by Fisk et al. (1999) under static testing conditions. Five sets of 10 vials containing 1 egg each were exposed to measured concentrations of 0.0014, 0.012, 0.120, 0.420, or 1.6 mg/L test substance starting after fertilization and terminating approximately 3 days post-hatch. No adverse effects were reported in exposed embryos. Concentrations of the test substance were found in larvae and eggs in a dose-dependent manner (with exception of the highest concentration) suggesting that the substance can diffuse through the egg. Corresponding measured concentrations in eggs were 0.04, 8.4, 63, 110, and 72 mg/kg and corresponding measured concentrations in larvae were 0.24, 8.2, 45, 84, and 51 mg/L. 
                  
                  EPA/OPPT Conclusion
                  The study was considered unacceptable primarily due to insufficient exposure duration and insufficient number of eggs per exposure concentration.

(5) The following summary provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was considered supportive, but did not characterize all fish life-cycle stages. Cooley et al. (2001) studied the toxicity of C14H24.9Cl5.1, 48%Cl (as described in Fisk et al., 1999) to juvenile rainbow trout (Oncorhynchus mykiss) through dietary exposure. Treatment groups of 10 fish were exposed to 0.78 and 2.9 mg/kg for 21 days and 0.082 mg/kg for 85 days. Three control groups were also run. Histological examination and analysis of the chlorinated paraffin concentration was performed in five fish per treatment after 21 days in the two higher test concentrations and in three fish per treatment after 85 days in the lowest test concentration. Three fish were also sacrificed from each low exposure group and the remaining control group (but were not analyzed) after 21 days of exposure. Quantitative histomorphological measurements were also carried out on livers and thyroid of the exposed fish in the middle exposure group after 21 days, and also the low exposure group after 85 days. The parameters investigated included hepatocyte nuclear diameter, hepatocyte volume index, nucleus:cytoplasm
area ratio and thyroid epithelium cell height. Livers displaying mild hepatocyte necrosis and moderate to severe depletion of glycogen/lipids were reported for the 0.78 mg/kg exposure. At 2.9 mg/L abnormal behavior was observed from day 3 onwards. Quantitative effects following 21 days of exposure were limited to a significantly (p=0.05) reduced mean hepatocyte volume in 2.9 mg/L exposure group. 

                  EPA/OPPT Conclusion
                  This study is considered unacceptable to characterize chronic mortality in fish because it did not characterize life stages but instead characterized physiological effects. 

(6) Cooley et al. (2001) studied the toxicity of another medium chain chlorinated paraffin with a slightly different chemical composition and at slightly different concentration levels. The chemical formula was [14]C-C14H23.3Cl6.7, 55% Cl (as described in Fisk et al., 1999) and was  juvenile rainbow trout (Oncorhynchus mykiss) were exposed through the diet. Treatment groups of 10 fish were exposed to 29 and 78 mg/kg for 21 days and 5.7 mg/kg for 85 days. Three control groups were also run. Histological examination and analysis of the chlorinated paraffin concentration was performed in five fish per treatment after 21 days in the two higher test concentrations and in three fish per treatment after 85 days in the lowest test concentration. Three fish were also sacrificed from each low exposure group and the remaining control group (but were not analyzed) after 21 days of exposure. Quantitative histomorphological measurements were also carried out on livers and thyroid of the exposed fish in the middle exposure group after 21 days, and also the low exposure group after 85 days. The parameters investigated included hepatocyte nuclear diameter, hepatocyte volume index, nucleus:cytoplasm area ratio and thyroid epithelium cell height. At 29 mg/kg abnormal behavior was observed from day 2 onwards and livers exhibited mild to moderate hepatocyte necrosis and moderate to severe depletion of glycogen lipids. Abnormal behavior from day 3 onward was also observed at 78 mg/kg.

                  EPA/OPPT Conclusion
                  This study is considered unacceptable to characterize chronic mortality in fish because it did not characterize life stages but instead characterized physiological effects. 
                  
(7)  The Dow Chemical Company (2009) 
Study title: Great Stuff(TM) Pond and Stone Waterfall Foam Filler: Evaluation of Potential Prolonged Toxicity to Freshwater Fish. Dow conducted a 14-day exposure of Great Stuff(TM) Pond and Stone Water Foam Filler to the fathead minnow (Pimephales promelas). The test substance used was Great Stuff(TM) Pond and Stone Water Foam Filler which is a urethane foam product dispensed from a pressurized steel canister using a finger-actuated valve/nozzle. Three 12 oz. canisters containing different developmental foam formulations (differing primarily in the colorant additive) were used. The test duration was 14 days and the exposure scenario was a static system which was renewed after 7 days. The test concentrations used were 0.15 and 0.63 g dry foam/: for each product tested and a water control. The test concentrations were equivalent to approximately 10 and 40 times the expected minimum foam loading for a typical pond application. Carrier solvents were not used in the test. The test solution volume was 15 L and the loading was 10 fish/15 L. The three foam samples were directly applied on the inside bottoms of identical 20 L glass aquaria and misted with MilliQ water to promote reaction/adhesion of the foam on the glass surface. The foam was applied along a longitudinal center line of the aquarium bottom, in a single continuous bead of approximately 2 cm diameter. Following application, the aquaria were loosely covered and foam was allowed to cure for 24 hours. After curing, the aquaria were rinsed, and then filled, with laboratory dilution water. Dissolved oxygen levels ranged from 6.8 - 7.9 mg/L (84 - 98% oxygen saturation) over the 14-day exposure period. Temperature, as measured daily from the individual test vessels and continuously measured from one surrogate test vessel, remained at 25°C throughout the study. The pH ranged from 7.1 - 7.7 and the light intensity ranged from 701 - 1,263 lux. Over the 14-day exposure period, no sublethal 
effects were observed in any of the treatments and only a single mortality was observed (observed on day 10 in one 40x treatment) and was believed to be incidental and non-treatment related, since no other fish in that test level exhibited signs of stress or sublethal effects during the test. Only DOC concentrations were measured to determine release of foam associated components. After seven days of contact with water, the foam-associated DOC resulting from the "10X" loading ranged from 0.6 to 0.9 mg/L for the three foam samples, and that from the "40X" loading ranged from 1.1 to 2.1 mg/L. None of the three foam products was consistently associated with the lowest or highest foam-associated DOC concentration, indicating that the three foam products did not have notable differences in their water-extractable components. The study did not completely characterize the chemical composition of the foam and did not fully identify the chlorinated paraffin composition, thus it is not possible to determine or characterize potential effects from chlorinated paraffin exposure. Only the chain length of the chlorinated paraffin was identified (C14-17) and the % Weight of the chlorinated paraffin in the foam product along with the chlorine content was not identified. Also, many of the components of the foam and % composition were also unidentified. In addition, the study duration was 14-days, a sub-chronic duration, and is not sufficient to characterize chronic population-level effects. 
                  EPA/OPPT Conclusion 
                  This study is considered unacceptable to characterize chronic population-level effects of MCCPs in fish. 

                  
 Chronic Aquatic Invertebrate Toxicity
(1) A 21-day chronic Daphnia magna reproduction toxicity study was conducted by Thompson et al. (1997b) according to OECD 202, Part II (1984) using a static-renewal test system with renewal 3 times/week. The test substance was identified as Cereclor S52[(R)], a C14-17 chlorinated paraffin with 52% chlorination that contained 0.3% epoxy soya bean oil stabilizer as well as a small amount of radiolabeled n-pentadecane-8-[14]C (51% chlorinated). Ten replicates of 1 Daphnia magna Straus (<24 hours old) were tested per exposure concentration, which did not comply with OECD 202, Part II requirements that at least 40 daphnid be tested per concentration. Nominal concentrations were 0 (dilution water control), 0 (solvent control), 0.0056, 0.01, 0.018, 0.032, 0.056, and 0.1 mg/L test substance in acetone (0.025 mL/L). Results from the acute daphnid study by the same author do not appear to have been considered when selecting concentrations for this study. Test solutions were prepared by adding the appropriate stock solution to dilution water while continuously and vigorously stirring with a magnetic follower. The submitter does not indicate whether renewal of the static-renewal test systems was carried out at regular intervals (e.g, Monday-Wednesday-Friday). Corresponding mean measured concentrations determined by radiochemical methods were 0.0037, 0.005, 0.01, 0.018, 0.032, and 0.065 mg/L and were 78-94% of nominal concentrations at the start of the renewal period and 7.3-61% of nominal concentrations at the end of the renewal period indicating a notable loss of test substance. Also, analysis of test concentrations appears to be at irregular intervals. In the dilution water control, 20% mortality was observed. Overall, dilution water control and solvent control results were significantly different for reproductive parameters. The test was carried out at temperatures of 19.5-20.3 °C, at pH levels of 7.41-8.13, and at dissolved oxygen concentrations of 6.2-9.2 mg/L. A significant decrease in the number of live offspring was reported at the mean measured concentration of 0.018 mg/L and delayed release of first offspring was observed at higher concentrations. Percentage dead offspring reported was 0%, 0%, 5.9%, 20.4%, and 18.5% for the 0.0037, 0.005, 0.01, 0.018, 0.032, and 0.065 mg/L mean measured exposures. 

                  EPA/OPPT Conclusion
                  The inability to maintain test concentrations, unspecified renewal periods, and a smaller population size may have affected subsequent reproductive results. Given the uncertainties of the test, reported effect levels may not represent a worst case scenario but do exhibit a clear dose response relationship with a clearly defined statistically significant effect level. Thus, using a weight of evidence approach, the study is considered acceptable for this endpoint.
                  21-day LC50 value of 0.025 mg/L (parent mortality)
                  21-d NOEC = 0.01 mg/L
                  21-d LOEC = 0.018 mg/L 
                  21-d GMATC = 0.013 mg/L 

(2) A 60-day mussel toxicity study was conducted by Brixham Laboratories in 1983 with radio-labeled chlorinated (52%) n-pentadecane (Trade Name: Cereclor S52[(R)]) under flow through testing conditions. A full non-CBI study report was submitted under TSCA in 1983 as DCN 40-8332184 (OTS Fiche 0507258). Blue mussels (Mytilus edulis) were exposed to nominal concentrations of 0 (dilution sea water control), 0 (acetone control, 500 ppm), 0.56, or 5.6 mg/L in 500 ppm acetone. Two replicates of 50 mussels were tested for the dilution water and solvent controls and a single replicate of 50 mussels was exposed for each treatment concentration. Corresponding mean measured concentrations were 0, 0, 0.22, and 3.8 mg/L. Test solutions were cloudy at the higher test concentration. Test concentrations were determined by radio activity measurements. Flow rate of the test system was 0.25 mL/minute for exposure concentrations. Over the course of the study, water temperature ranged from 14.6  -  15.6 °C, pH ranged from 8.0  -  8.3, and the dissolved oxygen concentrations ranged from 6.1  -  8.25 mg/L. Dilution water salinity was 34-35.5 ppb, which is high by OCSPP standards. 

                  EPA/OPPT Conclusion
                  One mussel exposed to 0.56 mg/L died, and two mussels exposed to the controls died; this was not considered to be a test substance related effect. Decreases in filter feeding were observed at 5.6 mg/L. In addition, the submitter provided an assessment of bioconcentration, but this assessment does not appear to include a depuration phase. Overall, the 60 day NOEC and LOEC were 0.22 and 3.8 mg/L based on reduced filtration. The study was acceptable to characterize mussel toxicity, but mussels are not considered a standard species to fulfill the chronic aquatic invertebrate toxicity endpoint.
                  60-d NOEC = 0.22 mg/L
                  60-d LOEC = 3.8 mg/L (reduced filtration)

(3) The following study summary (Frank, 1993; Frank and Steinhäuser, 1994) provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was considered supportive of the aquatic invertebrate hazard determination. A 21-day chronic Daphnia magna reproduction toxicity study was conducted using a static-renewal test system (renewal 3 times/week). The test substance was identified as C14-17 chlorinated paraffin with 52% chlorination, which was tested as a water soluble fraction of two stock solutions (dilutions used 1:2 to 1:32). Nominal test concentrations prepared from the 100 mg/L stock solution were 3.125, 6.25, 12.5, 25, and 50 mg/L. Nominal test concentrations prepared from the 10,000 mg/L stock solution were 312.5, 625, 1250, 2500, and 5000 mg/L. Analytical monitoring of test concentrations was conducted, but only the final effect levels were presented as measured concentrations. Methods for test solution preparation were not provided in the summary. The tests were carried out at 20 °C and at  pH 7.79-8.44. 

In the experiments using the 100 mg/L stock solution the mortality seen in the exposed populations was 0% at 3.125 mg/L, 0% at 6.25 mg/L, 20% at 12.5 mg/L, 90% at 25 mg/L, and 100% at 50 mg/L. In the experiments using the 10,000 mg/L stock solution the mortality seen in the exposed populations was 0% at 312.5 mg/L, 30% at 625 mg/L, 70% at 1250 mg/L, and 100% at lower dilutions (>1250 mg/L). In the experiments using the 100 mg/L stock solution the average number of young/adult was 82 at 3.125 mg/L, 89 at 6.25 mg/L, 80 at 12.5 mg/L, 15 at 25 mg/L and 0 at 50 mg/L (all parents died). Similarly in the experiments using the 10,000 mg/L stock solution the average number of young/adult was 74 at 312.5 mg/L, 64 at 625 mg/L, 43 at 1250 mg/L, and 0 at 2,500 and 5,000 mg/L (all parents died). Based on these effects, survivability/mortality appears to be the more sensitive endpoint. Based on the known measured concentrations in the stock solutions and the dilution rates used the NOEC for mortality was around 0.0044-0.0089 mg/L for the 100 mg/L nominal stock solution experiments and 0.0126-0.0156 mg/L for the 10000 mg/L nominal stock solution experiments. The corresponding LOECs were 0.0089- 0.0178 mg/L (100 mg/L nominal stock) and 0.0253-0.0313 μg/L (10 g/L nominal stock). The GMATC of 0.006 mg/L was calculated using the geometric mean from the most conservative NOEC (0.0044 mg/L) and LOEC (0.0089 mg/).

                  EPA/OPPT Conclusion
                  EPA/OPPT reserves judgment on the acceptability of this study until further details become available.
                  21-d NOEC = 0.0044 mg/L
                  21-d LOEC = 0.0089 mg/L 
                  21-d GMATC = 0.006 mg/L 

3) The following study summary (TNO, 1993) provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was considered supportive of the aquatic invertebrate hazard determination. A 21-day chronic Daphnia magna reproduction toxicity study was conducted using a static-renewal test system (renewal 3 times/week). The test substance was identified as C14-17 chlorinated paraffin with 52% chlorination. The test solutions were prepared by stirring 20 g of the test substance in 2 litres of heated water (60 °C) with stirring and then filtration through a 0.8 um and 0.2 um filter. This resulting stock solution was referred to as a water soluble fraction, but given that each concentration was not independently prepared, the test solutions is considered by EPA/OPPT to be merely a mixed and filtered solution that was subsequently diluted. Following dilution of the stock solution, exposure concentrations were analytically determined using the extractable organic halogen method, but not provided in the study summary. The test was carried out at 20 +- 1 ºC and solutions were gently aerated from day 9 onwards. The pH of the test water varied between 7.7 and 8.3, the dissolved oxygen concentration was > 7 mg/L, and the hardness was 214 mg CaCO3/L. Test solutions were clear. 

                  EPA/OPPT Conclusion
                  Although analytical results obtained were considered to be too erratic to allow precise determination of concentrations (according to the study summary in ECB, 2005), the NOEC was reported based on survivability and/or reproductive effects. A LOEC in mg/L was not reported in the summary, nor could EPA/OPPT extrapolate one. EPA/OPPT reserves judgment on the acceptability of this study until further details become available.
                  21-d NOEC = 0.004-0.008 mg/L
                  

 Chronic Aquatic Sediment Invertebrate Toxicity
1) Thompson et al. (2001c) conducted a 28-day prolonged sediment invertebrate toxicity study with spiked sediment was conducted according to OECD 218 draft guideline (February 2000 version) using a static test system. The substance used in the test was commercial C14-17, 52% wt. Cl substance containing no stabilizers (the substance was reported to have a C14-17 content of 99.06% with 0.67% of C10-13 chain length substances) that was mixed with a small amount of a radio labeled n-pentadecane-8-[14]C, 51% wt. Cl substance (radiochemical purity >96.6%). The sediment used in the test was an artificial sediment that did not fully adhere to the final OECD TG recommendations, but the composition of 10% sphagnum moss peat, 70% quartz sand, 20% kaolinite clay, and <0.1% calcium carbonate are not considered to be significantly different. The sediment had a mean organic carbon content of 4.9% and a pH of 6.0. The sediment was spiked with the test substance by firstly mixing a solution of the test substance in acetone with the dry sand component of the sediment and allowing the acetone to evaporate overnight under an air stream. Measured concentrations were determined using radiochemical analysis. Over the course of the study, temperature was maintained at 20 ºC, pH levels were 6.2-7.6, and dissolved oxygen in overlying water was maintained at 7.3-8.6 mg/L. Three replicates of 15 midge (Chironomus riparius) larvae (<48 hours post hatch) were exposed to mean measured concentrations of 0 (sediment control), 0 (solvent sediment control), 36, 110, 370, 1200, 3800, or 13000 mg/kg dry wt. sediment. Time to first emergence, mean emergence time, mean number emerged per replicate, and sex ratio was assessed for each exposure group. Statistically significant effects (p = 0.05) were limited to a decrease in mean number emerged per replicated in the 13,000 mg/kg dry wt. sediment exposed midges.

                  EPA/OPPT Conclusion
                  The overall NOEC of 3,800 mg/kg dry wt. sediment corresponded to 1,460 mg/kg on a wet weight basis. The study is acceptable.
                  28-d NOEC = 3,800 mg/kg dry wt sediment
                  28-d LOEC = 13,000 mg/kg dry wt sediment
                  28-d GMATC = 7,029 mg/kg dry wt sediment

2) Thompson et al. (2001d) conducted a 28-day prolonged sediment invertebrate toxicity study with spiked sediment according to methods described in Phipps et al. (1993) using a static test system. The substance used in the test was commercial C14-17, 52% wt. Cl substance containing no stabilizers (the substance was reported to have a C14-17 content of 99.06% with 0.67% of C10-13 chain length substances) that was mixed with a small amount of a radio labelled n-pentadecane-8-14C, 51% wt. Cl substance (radiochemical purity >96.6%). The sediment used in the test was an artificial sediment consisting of 10% sphagnum moss peat, 70% quartz sand, 20% kaolinite clay, and <0.1% calcium carbonate. The sediment had a mean organic carbon content of 4.9% and a pH of 6.0. The test sediments were made up by adding the test substance to the sand phase as a solution in acetone, evaporating the acetone overnight and mixing the spiked sand with the rest of the sediment for 16 hours. Six replicates of 10 oligochaete (Lumbriculus variegatus) adults were exposed to mean measured concentrations of 0 (sediment control), 0 (solvent sediment control), 39, 130, 410, 1300, 4000, or 13000 mg/kg dry wt. sediment. Throughout the duration of the study, water temperature was maintained at 20 +- 1 Cº, and pH remained between 6.3 and 7.9. Mortality and reproductive success were determined by total number of worms at study termination since differentiation of adult and young worms is difficult. Mean number of worms per replicate and mean total dry weight of worms per replicate was significantly different from controls (p = 0.01) at mean measured concentrations of 410 mg/kg dry weight sediment and greater. Statistical methods used were not reported, and a p-value of 0.01 was used.
                  
                  EPA/OPPT Conclusion
                  Given that a clear decline in the mean number of worms per replicate and mean total dry weight of worms per replicate was observed at the lowest test concentration (39 mg/kg dry weight sediment) a conservative LOEC of 39 mg/kg dry weight sediment will be used based on noticeable differences. EPA/OPPT reserves judgment on the acceptability of this study until further details become available regarding the analytical measurements of the chlorinated paraffin mixture.
                  28-d NOEC = 130 mg/kg dry wt sediment
                  28-d LOEC = 410 mg/kg dry wt sediment
                  GMATC = 230.9 mg/kg dry wt sediment

3) Thompson et al. (2002) conducted a 28-day prolonged sediment toxicity study with amphipod Hyalella azteca in spiked sediment using a static-renewal test system with weekly renewals. The substance used in the test was a mixture of a commercial medium-chain chlorinated paraffin product (C14-17, 52.5% wt. Cl) mixed with a small amount of a radiolabeled chlorinated n-pentadecane-8-14C (51% wt. Cl). The sediment used in the test was an artificial sediment consisting of 10% sphagnum moss peat, 70% quartz sand, 20% kaolinite clay, and <0.1% calcium carbonate. The sediment had a mean organic carbon content of 4.9% and a pH of 6.0. The test sediments were made up by adding the test substance to the sand phase as a solution in acetone, evaporating the acetone overnight and mixing the spiked sand with the rest of the sediment and water. Six replicates per concentration of ten juvenile Hyalella azteca (~7-day-old) were exposed to 0 (sediment control), 0 (acetone sediment control), 38, 75, 150, 300, or 600 mg/kg dry weight sediment. The concentration of the test substance was measured in the sediment phase by radiochemical analysis with concentrations at the start of the exposure period of 85-97% of the nominal values and concentrations at the end of the 29-day exposure period of 78-90% of nominal. Results of the test were expressed as the arithmetic mean concentration. Over the course of the study, dissolved oxygen ranged from 7.7 to 8.4 mg/L, pH ranged from 7.0 to 7.6, water hardness ranged from 41 to 42 mg CaCO3/L, and temperature ranged from 22.4-23.2ºC. The endpoints investigated in the study included survival, growth (dry weight) and sexual development of females (proportion of gravid females). 

                  EPA/OPPT Conclusion
                  Controls responded adequately. For the survival endpoint, a statistically significant (p=0.05) reduction in survival was seen at 470 mg/kg dry weight. A statistically significant reduction in mean weight was seen in females only at exposures of 470 g/kg dry weight sediment and a statistically significant (p=0.05) reduction in mean weight was seen at 270 mg/kg dry weight. For the sexual development endpoint, there was a statistically significant (p=0.05) reduction in the proportion of gravid females in the 470 mg/kg dry weight treatment. This study was acceptable.
                   28-d NOEC = 130 mg/kg dry wt sediment
                  28-d LOEC = 270 mg/kg dry wt sediment
                  28-d GMATC = 187 mg/kg dry wt sediment

 Avian Toxicity
(1) An acute avian toxicity study conducted according to OPPTS guidelines was published by Madeley & Birtley (1980). Following a range-finding study, groups of 5 male and 5 female ring-necked pheasants (Phasianus colchicus) were exposed by gavage to 0 (control) or 24,606 mg/kg Cereclor S52[(R)]  (C14-17, 52% Cl) and then observed for 14 days. Based on reported tissue concentrations, the test substance is believed to have been absorbed by the ring-necked pheasant. Doses up to 24,606 mg/kg failed to produce any abnormal clinical signs or mortality.
                  
                  EPA/OPPT Conclusion
                  Acute LD50 > 24,606 ppm

(2) An acute avian toxicity study conducted according to OCSPP guidelines was published by Madeley & Birtley (1980). Following a range-finding study, groups of 5 male and 5 female mallard ducks (Anas platyrynchos) were exposed by gavage to 0 (control) or 10,280 mg/kg Cereclor S52[(R)]  (C14-17, 52% Cl) and then observed for 14 days. Based on reported tissue concentrations, the test substance is believed to have been absorbed by the mallard ducks. Doses up to 10,280 mg/kg failed to produce any abnormal clinical signs or mortality.
                  
                  EPA/OPPT Conclusion
                  Acute LD50 > 10,280 ppm

(3) A sub-acute dietary avian toxicity study conducted according to OPPTS guidelines was published by Madeley & Birtley (1980). Following a range-finding study, groups of 5 male and 5 female ring-necked pheasants (Phasianus colchicus) were exposed to diets containing 0 (control), 1,000, or 24,063 ppm Cereclor S52[(R)]  (C14-17, 52% Cl) for 5 days. Three groups were exposed to the negative control and two groups were exposed to each of the treatment concentrations. Based on reported tissue concentrations, the test substance is believed to have been absorbed by the ring-necked pheasant. Good health was noted in all control and treatment groups. No abnormal effects were noted at necropsy.

                  EPA/OPPT Conclusion
                  5-day LD50 > 24,063 ppm

(3) A sub-acute dietary avian toxicity study conducted according to OPPTS guidelines was published by Madeley & Birtley (1980). Following a range-finding study, groups of 5 male and 5 female mallard ducks (Anas platyrynchos) were exposed to diets containing 0 (control), 1,000, or 24,063 ppm Cereclor S52[(R)]  (C14-17, 52% Cl) for 5 days. Three groups were exposed to the negative control and two groups were exposed to each of the treatment concentrations. Inferior food intake was noted for ducks, but weight gain was comparable to controls. Based on reported tissue concentrations, the test substance is believed to have been absorbed by the mallard ducks. Good health was noted in all control and treatment groups. No abnormal effects were noted at necropsy.

                  EPA/OPPT Conclusion
                  5-day LD50 > 24,063 ppm
 Terrestrial Invertebrate Toxicity
1) A 28-day earthworm reproductive toxicity test was conducted by Thompson et al., 2001a according to OECD guideline (2000 draft version). The substance tested was commercial C14-17, 52% wt. Cl substance containing no stabilizers (the substance was reported to have a C14-17 content of 99.06% with 0.67% of C10-13 chain length substances) and a small amount of 14C-labelled n-pentadecane, 51% wt. Cl substance. Four replicates per concentration of 10 adult earthworm (Eisenia fetida) were exposed to nominal concentrations of 0 (soil control), 0 (solvent soil control), 100, 320, 1000, 3200, or 10,000 mg/kg dry wt. soil. Corresponding mean measured concentrations of 0 (soil control), 0 (solvent soil control), 79, ~280, 900, ~2,800, or 9,300 mg/kg dry wt. was determined using radiochemical analysis; concentrations identified as approximate (~) were approximated using the mean% of nominal (87%) determined in other treatments. Measured tissue concentrations in adults on day 28 were 169, 802, and 732 mg/kg wet weight for the 79, 900, and 9,300 mg/kg dry weight exposure groups. Measured tissue concentrations in juveniles on day 56 were 140 and 1,011 mg/kg wet weight for the 79 and 900 mg/kg dry weight exposure groups. The soil used in the test was an artificial soil consisting of 10% sphagnum moss peat, 70% quartz sand, 20% kaolinite clay, and 0.25% calcium carbonate. The soil had an organic carbon content of 4.7% and a pH of 6.66-7.09. Nominal test temperatures remained at 20 +- 1 ºC. The soils were prepared up by firstly adding the test substance in solution with acetone to a small portion of soil, evaporating out the acetone overnight under a stream of compressed air, and then mixing with the remainder of the soil. Before use, distilled water was added to the dry soil to provide a soil wet:dry ratio of 1.35. Following the 28-day parental exposure period, adult earthworms were removed, and vessels were incubated for an additional 28 days to allow hatching of any egg cocoons produced by parent. Effects assessed were parental survival, growth as determined by change in weight of parents, and reproduction as determined by number of live offspring. A statistically significant (p = 0.05) reduction in parental survival (85%) was observed at 9,300 mg/kg dry wt. soil. A statistically significant (recalculated with Dunnett's Procedure, P = 0.05) reduction in parental weight was reported at 2800 mg/kg dry wt. soil. A statistically significant (recalculated with Dunnett's Procedure, P = 0.05) reduction in number of live offspring was reported at 280 mg/kg dry wt. soil. In addition, the submitter assesses corresponding tissue concentrations in earthworms and determines that at nominal concentrations of 100 mg/kg dry wt. soil the concentration in parental earthworm tissue after 28 days is 850 mg/kg dry wt.and in juvenile worms after 56 days was 703 mg/kg dry wt. 

                  EPA/OPPT Conclusion
                  The study was acceptable.
                  28-d NOEC = 79 mg/kg dry wt soil
                  28-d LOEC = 280 mg/kg dry wt soil
                  28-d ChV = 149 mg/kg dry wt soil

2) The following study summary (Thompson et al., 2001a) provided in the 2005 European Chemical Bureau Risk Assessment of MCCP was used to characterize terrestrial invertebrate hazard in a screening level risk assessment. A 28-day earthworm reproductive toxicity test was conducted according to OECD guidelines. The substance tested was commercial C14-17, 52% wt. Cl substance containing no stabilizers (the substance was reported to have a C14-17 content of 99.06% with 0.67% of C10-13 chain length substances). The test substance contained a small amount of 14C-labelled n-pentadecane, 51% wt. Cl substance so that radiochemical analysis could be used to analytically determine test concentrations in soil. The soil used in the test was an artificial soil consisting of 10% sphagnum moss peat, 70% quartz sand, 20% kaolinite clay, and 0.25% calcium carbonate. The soil had an organic carbon content of 4.7% and a pH of 6.66-7.09. The soils were prepared up by firstly adding the test substance in solution with acetone to a small portion of soil, evaporating out the acetone overnight under a stream of compressed air, and then mixing with the remainder of the soil. Before use, distilled water was added to the dry soil to provide a soil wet:dry ratio of 1.35. Four replicates per concentration of 10 adult earthworm (Eisenia fetida) were exposed to mean measured concentrations of 0 (soil control), 0 (solvent soil control), 79, ~280, 900, ~2800, or 9300 mg/kg dry wt. for 28 days; concentrations identified as approximate (~) were approximated using the mean% of nominal (87%) determined in other treatments. Measured tissue concentrations in adults on day 28 were 169, 802, and 732 mg/kg wet weight for the 79, 900, and 9300 mg/kg dry weight exposure groups. Measured tissue concentrations in juveniles on day 56 were 140 and 1011 mg/kg wet weight for the 79 and 900 mg/kg dry weight exposure groups. Following the 28-day parental exposure period, adult earthworm were removed, and vessels were incubated for an additional 28 days to allow hatching of any egg cocoons produced by parent. Effects assessed were parental survival, growth as determined by change in weight of parents, and reproduction as determined by number of live offspring. Statistical methods used to calculate significance were not provided. A statistically significant (p = 0.05) reduction in parental survival (85%) was observed at 9300 mg/kg dry wt. soil. A statistically significant (p = 0.01) reduction in parental weight was reported at 2800 mg/kg dry wt. soil and a noticeable reduction in parental weight was reported at 280 mg/kg dry wt. soil. A statistically significant (p = 0.01) number of live offspring was reported at 1000 mg/kg dry wt. soil and a noticeable reduction in number of live offspring was reported at 320 mg/kg dry wt. soil. A clear decline in parental weight and number of live offspring was observed at 280 mg/kg dry wt. soil.

                  EPA/OPPT Conclusion
                  This study is acceptable.
                  28-d NOEC = 79 mg/kg dry wt soil 
                  28-d LOEC = 280 mg/kg dry wt soil
                  28-d GMATC = 149 mg/kg dry wt soil

 Terrestrial Plant Toxicity
1) Thompson et al., 2001ab conducted a 28-day seed germintation and vegetative vigor study. The toxicity of a C14-17, 52% wt. Cl substance (99.06% purity) to wheat (Triticum aestivum; monocotyledon), oilseed rape (Brassica napus; ditcotyledon), and mung bean (Phaseolus aureus; dicotyledonous legume) has been studied using OECD guideline 208 (July, 2000 Revision). The test substance contained a small amount of 14C-labelled n-pentadecane, 51% wt. Cl substance so that radiochemical analysis could be used to analytically determine test concentrations in soil. The soils were prepared up by firstly adding the test substance in solution with acetone to dry silver sand, evaporating the acetone overnight, and mixing the spiked sand with the soil. Four replicate pots per exposure concentration each containing 9 seeds were exposed for 28 days to nominal exposure concentrations of 0 (soil control), 0 (solvent soil control), 50, 158, 500, 1,580, or 5,000 mg/kg dry wt.. According to the E.U. Risk Assessment, use of nominal test concentrations to determine effect levels is based on test substance stability determined at the 50, 500, and 5,000 mg/kg dry wt. concentrations (corresponding mean measured concentrations: 49, 520, and 5,800 mg/kg dry wt.). Effects assessed were seed germination, emergence (% emerged plants on Day 14), vegetative growth (mean shoot dry weight per plant), and visual appearance of seedling. No statistically significant differences (p = 0.05) were observed in wheat, oilseed rape. A statistically significant reduction in growth was seen at 1,580 and 5,000 mg/kg dry wt. for mungbean when compared to soil control results.

                  EPA/OPPT Conclusion
                  Since soil control and solvent control means were equal (two tailed T-Test) indicating no solvent interference, comparison of treatments was made to the soil control. Thus, the NOEC and LOEC for terrestrial plants was 500 and 1,580 mg/kg dry wt. soil and the GMATC (geometric mean of the NOEC and LOEC) was 888.8 mg/kg dry wt. soil. The study was acceptable to characterize both monocot (wheat) and dicot (mung bean) seed germination and vegetative vigor; reproductive effects remain uncharacterized.
                  28-d NOEC = 500 mg/kg dry wt soil
                  28-d LOEC = 1,580 mg/kg dry wt soil
                  28-d GMATC = 888.8 mg/kg dry wt soil

 Conclusions 
Sufficient data were available to characterize the acute fish, the acute aquatic invertebrate, the chronic aquatic invertebrate, the chronic aquatic sediment invertebrate, avian, and terrestrial plant toxicity endpoints for MCCPs. Data for other toxicity endpoints (i.e., chronic fish, aquatic plant, etc.) were inconclusive due to lack of study details, uncertainties in analytical methods, or test material preparation methods; thus, these data are included in order to characterize risk in a qualitative manner, but are used as supportive for the categories under which they are provided. Supporting data were included in order to provide a weight-of-evidence approach used to characterize some endpoints. 

Most of the data provided in this review indicated several difficulties were encountered when testing in an aquatic environment. These included: (1) getting the material into solution, (2) measuring the material in solution, and (3) characterizing the effects for each study listed. Often there were many details of a given study omitted, prohibiting a full and robust review of the data. The (estimated) physical-chemical properties of MCCPs (water solubility values of approximately 30 μg/L and Log Kow values between 4-8) suggest these materials may not partition to the aquatic media or elicit toxicity to aquatic organisms within the water column. 

The most reliable and acceptable studies indicate that for MCCPs, the toxicity to aquatic organisms for acute endpoints are from the Thompson et al. 1996 study for aquatic invertebrates. Where the 48-hour EC50 value = 0.0059 mg/L. Using the methods described in the Sustainable Futures/P2 Manual (US EPA, 2012), the acute and chronic concentrations of concern (CoC) are derived as follows:
 Acute CoC: The 48-hour EC50 value = 0.0059 mg/L is divided by an assessment factor of 5 to yield an acute concentration of concern (CoC) of 0.00118 mg/L, or 0.001 mg/L, or 1 μg/L (1 ppb). Aquatic Acute Concern Concentration= 1 ppb
 Chronic CoC: The aquatic invertebrate chronic value of 0.013 mg/L from the 1997 Thompson et al. study based on a MCCP material is divided by an assessment factor of 10 to yield 0.0013 mg/L or 1.3 μg/L or 1.3 ppb. Aquatic Chronic Concern Concentration = 1 ppb

The most reliable and acceptable value for the toxicity to aquatic sediment invertebrate organisms acute endpoint is based on the MCCP material from the Thompson et al. 2002 28-d study. The 28-d sediment invertebrate GMATC value of 187 mg/kg dry wt sediment is used to assess hazard. Again, using methods in US EPA (2012): 

 Acute CoC: Calculating an acute concern concentration from the chronic value of 187 mg/kg dry wt. The 187 value is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,870 mg/kg dry wt. This value is then divided by an assessment factor of 5 to yield 374 mg/kg dry wt. Aquatic Sediment Acute Concern Concentration = 374 mg/kg dry wt sediment.
 Chronic CoC: The 28-d sediment invertebrate GMATC of 187 mg/kg dry wt sediment is divided by an assessment factor of 10 to yield 18.7 mg/kg dry wt sediment. Aquatic Sediment Chronic Concern Concentration = 19 mg/kg dry wt sediment.

The most reliable and acceptable value for the toxicity to terrestrial invertebrates acute endpoint is based on the MCCP material from the Thompson et al. 2001a study. The 28-d terrestrial invertebrate GMATC value of 149 mg/kg dry wt sediment from this study will be used. 
Again, using methods in US EPA (2012): 

 Acute CoC: Calculating an acute concern concentration from the chronic value of149 mg/kg dry wt, this value is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,490 mg/kg dry wt. This value is then divided by an assessment factor of 5 to yield 298 mg/kg dry wt. Terrestrial Invertebrate Acute Concern Concentration = 298 mg/kg dry wt sediment.
 Chronic CoC: The 28-d terrestrial invertebrate GMATC of 149 mg/kg dry wt is divided by an assessment factor of 10 to yield 14.9 mg/kg dry wt sediment. Terrestrial Invertebrate Chronic Concern Concentration = 15 mg/kg dry wt sediment.

The most reliable and acceptable value for the toxicity to terrestrial plants is based on the MCCP material from the Thompson et al. 2001ab study. For LCCPs, the analog approach using the values from this study may be used. However, there is no OPPT guidance regarding assessing concern concentrations for terrestrial plants. 

 LCCP ECOTOXICITY DATA
Where data are absent for long chain chlorinated paraffins for ecotoxicity endpoints, data from sources using medium chain chlorinated paraffins will be used to inform the hazard for these endpoints. 

 Acute Fish Toxicity
(1)  Johnson and Finely 1980 
A series of 96-hour acute fish toxicity studies were conducted by the United States Geological Survey's Columbia National Fisheries Research Laboratory, over the years 1965  -  1978, with several long-chain chlorinated paraffins (Chlorowax LV, C>17, 39% Cl; Chlorowax 40, C>20, 40 - 42% Cl; Chlorowax 50, C>20, 48 - 54% Cl; Chlorowax 70, C>20, 70% Cl) published by Johnson and Finely (1980). Bluegill sunfish (Lepomis macrochirus) and rainbow trout (Oncorhynchus mykiss) were exposed to the test substance (100% commercial formulation) in a static test system. Stock solutions were prepared immediately before each test with acetone used as a carrier solvent. The average pH level was between 7.2 and 7.5 for all tests and the test temperature was 20 +- 1°C for Bluegill sunfish and 10 +- 1 ºC for Rainbow trout. Dilution water hardness ranged from 40 to 50 mg/L as CaCO3. Reported effect levels are considered to be nominal with LC50 values of >300 mg/L for bluegill sunfish and rainbow trout for all LCCPs tested; all values are above the limit of solubility.
                  EPA/OPPT Conclusions
                  Using a weight-of-evidence approach, these studies were considered acceptable to characterize the acute fish toxicity endpoint.
                  96-hr LC50 = NES (> 300 mg/L)
                  
(2) Bengtsson et al. 1979
A 96-hour acute fish toxicity study as part of a bioaccumulation study was published by Bengtsson et al. (1979).  Bleak (Alburnus alburnus) were exposed to a long-chain chlorinated paraffin, Witaclor 549 (C18-26, 49% Cl). The test was performed at 10 °C under semi-static testing conditions. A nominal concentration of 0.125 mg/L was prepared by first dissolving Witaclor in acetone and then added to the dilution water. The treatment vessels and acetone control vessels consisted of six groups of 15 fish (average 4.5 g per fish). The acetone in all treatments did not exceed 0.1 ml/L. The test solutions were renewed every two to three days over the 14-day exposure period. Specific details of the test conditions were not provided other than the tests were performed at 10°C in seawater with a salinity of 7 ppt. Even though the test duration was 14-days, no mortality occurred within 96-hours or 14-days, thus the 96-hour LC50 was > 0.125 mg/L. 

                  EPA/OPPT Conclusions
                  This study was considered supplemental to characterize the acute saltwater fish toxicity endpoint using a weight-of-evidence approach. 
                   96-hr LC50 = NES (> 0.125 mg/L)

 Acute Aquatic Invertebrate Toxicity
(1) Frank (1993) and Frank and Steinhäuser (1994)
The following study summary (Frank, 1993; Frank and  Steinhauser, 1994), provided in the ECB (2005) MCCP risk assessment, was considered supportive of the aquatic invertebrate hazard determination. The chlorinated paraffin used in these studies was a commercial C14-17 product with a 52 wt% Cl. Daphnia magna were exposed to nominal concentrations of either 100 mg/L or 10,000 mg/L. The 100 mg/L solution was sonicated for 1 hour and then left to stand in the dark for 48 hours before use. The 10,000 mg/L solution also stood for 48 hours in the dark before use, but this time without sonication. After this period, both solutions were filtered firstly with glass filters and then with membrane filters to remove undissolved test substance. The concentrations of medium-chain chlorinated paraffin in the water soluble fractions were then determined by AOX (adsorbable organic halogen) analysis (detection limit of 10 μg/L Cl was equivalent to around 20 μg/L of the chlorinated paraffin). This analysis showed that the concentration of chlorinated paraffin present in the water soluble fraction was around 0.404 - 0.500 mg/L for the 10,000 mg/L nominal solution and 0.071 - 0.142 mg/L for the 100 mg/L stock solution. The acute (48-hour) toxicity tests were carried out using dilutions of the two prepared water soluble fractions. The method used was DIN 38 412, Teil 11, which is equivalent to OECD 202. 

In the tests using the water soluble fraction from the 100 mg/L nominal solutions no toxicity was seen at concentrations up to the undiluted stock solution (i.e., no effects up to around 0.071-0.142 mg/L). In experiments using the water soluble fraction from the 10,000 mg/L stock solution, an EC0 of 0.140 mg/L (also reported as 0.100 - 0.110 mg/L in the paper) and an EC25 of 0.423 mg/L (also reported as 0.420-0.470 mg/L in the paper) was determined (maximum mortality seen was 25%) (Frank, 1993). The latter results for the 10,000 mg/L stock solution were reported by Frank and Steinhauser (1994) as EC0 = 0.140 mg/L and EC25 = 0.339 mg/L, and it was noted that some of the Daphnia were floating on the surface of the test solution. In the later study (Frank and  Steinhauser, 1994), the results of further acute toxicity studies were reported using the same test method. An EC50 of 0.037 mg/L and an EC0 of 0.009 mg/L were determined using the water soluble fraction from the 100 mg/L stock solution and no toxic effects were seen in tests with the water soluble fraction from the 10,000 mg/L stock solution (approximately EC0 >= 0.525 mg/L). The authors noted that the effects seen in the acute tests showed poor reproducibility, probably because effects were seen only around the water solubility limit of the substance. However, the authors thought that the possibility of undissolved droplets affecting the results could be ruled out, as floating Daphnia were only sporadically observed in the test.

                  EPA/OPPT Conclusions
                  This study could not be adequately assessed due to inconsistencies in the hazard data for the different dilutions of the test material. In addition, the authors noted that the effects seen showed poor reproducibility, most likely due to effects observed only around the solubility limit in the test system used. The results of this test should therefore be treated with caution, as the effects were mainly seen in the saturated solutions only.

(2)  Tarkpea et al. 1981
The Tarkpea et al. (1981); as quoted in IPCS (1996) summary, provided in the ECB (2005) MCCP risk assessment, was considered supportive of the aquatic invertebrates hazard determination. 

The results of tests with the brackish water harpacticoid Nitocra spinipes have been reported (Tarkpea et al., 1981). No other details of the test were reported but the test method was probably the same as reported by Tarkpea et al. (1981), where a static method was employed using water of salinity 7%. at a temperature of 20 - 22°C without aeration, probably using acetone as co-solvent.

                  EPA/OPPT Conclusions
                  This study could not be adequately assessed due to the lack of details provided regarding specific conditions of the test and the preparation of the test solutions. The lack of detail prohibits a review and adequacy of the study. However, the harpaticoid, Nitocra spinipes, is not a standard test species and the test concentrations greatly exceed the limit of solubility. The 96-hour LC50 values for both chlorinated paraffins were identified, but the reliability of the results cannot be determined. Overall, EPA/OPPT reserves judgment on the acceptability of this study. Therefore, data from sources using medium chain chlorinated paraffins will be used to inform the hazard for these endpoints. 

 Aquatic Plant Toxicity
(1)  Koh and Thiemann 2001
A 72-hour algae toxicity study using Scenedesmus subspicatus, was conducted at the University of Bremen, Department of Physical and Environmental Chemistry with CP 30 (C17-24, 35% chlorination), CP 40 (C17-20, 44% chlorination) and Hordaflex LC50 (C17-20, 52% chlorination) according to DIN 38412 by Koh and Thiemann (2001). Additional communications with the study author Wolfram Thiemann clarified that nominal test concentrations and local tap water (Bremen, Germany) was used without adjustments however, the study methods were not fully characterized. The stock solutions were prepared to a concentration 6 mg/mL of test substance in acetone. The individual stock solutions were diluted with distilled water to prepare individual standard solutions of 0.250 mg/L for CP 30 and CP 40 and 0.125 mg/L for Hordaflex LC 50. pH was between 5 and 6 and water hardness was between 35.7 and 53.5 mg CaCO3/L. Ambient laboratory air temperature was ~ 21 ºC. The solvent acetone was used to maintain test substance in solution. Effects were calculated based on growth rate; no effects were observed up to 0.250 and 0.125 mg/L.

                  EPA/OPPT Conclusions
                  All three of the chlorinated paraffins tested contain C17 and C18 constituents which are considered to have LCCP-like properties. More information concerning composition would be needed to accept these results for long-chain chlorinated paraffins. Overall, EPA/OPPT reserves judgment on the acceptability of this study.
                  72-hr EC50 (growth rate) = NES (> 0.250 mg/L; CP 30 and CP 40)
                  72-hr EC50 (growth rate) = NES (> 0.125 mg/L; Hordaflex LC 50)
                  72-hr NOEC >= 0.250 mg/L (CP 30 and CP 40)
                  72-hr NOEC >= 0.125 mg/L (Hordaflex LC 50)

 Chronic Fish Toxicity
No data are available.

 Chronic Aquatic Invertebrate Toxicity
(1) Frank 1993 and Frank Steinhäuser 1994 
The following data review of Frank (1993) and Frank and Steinhäuser (1994) were directly excerpted from the U.K. Environmental Risk Assessment of long-chain chlorinated paraffins: 
                  
   The test substance was identified as C18-20 chlorinated paraffin with 52% chlorination. Frank (1993) carried out a series of acute and longer-term studies with Daphnia magna using a commercial C18-20, 52% wt. Cl product. The tests were carried out using dilutions of the water-soluble fraction of the chlorinated paraffin. Stock solutions of the chlorinated paraffin were made up in water to give nominal concentrations of either 100 mg/L or 10 g/L. The 100 mg/L solution was sonicated for one hour and then left to stand in the dark for 48 hours before use. The 10 g/L solution also stood for 48 hours in the dark before use, but this time without sonication. After this period, both solutions were filtered firstly with glass filters and then with membrane filters to remove undissolved test material (microscopic and spectroscopic investigation of the filtered solutions gave no indication of the presence of droplets) to give the respective water-soluble fractions. The concentration of the chlorinated paraffin in the water-soluble fractions was determined by AOX (adsorbable organic halogen) analysis. The detection limit of the method used was around 10 μg Cl/L, which is equivalent to around 20 μg/L of the chlorinated paraffin. This analysis showed that the concentration of chlorinated paraffin present in the water-soluble fraction was around 462 - 519 μg/L for the 10 g/L nominal solution but was not detectable in the 100 mg/L solution (i.e. <20 μg/L). Experiments were carried out to show that in the test vessels, although the concentration of chlorinated paraffin present fell over time, it remained within 80 per cent of the initial concentration over 2 - 3 days. This time period was used in the long term tests as the renewal period for the solution (semi-static method).
      
   Long-term (21-day) reproduction studies were also performed using dilutions of the water-soluble fractions of the two stock solutions. The dilutions used were 1:2, 1:4, 1:8 and 1:16 for the 100 mg/L loading and 1:4, 1:8, 1:16, 1:32 and 1:64 for the 10 g/L loading. In these experiments, the test medium was changed three times per week and 10 animals were used per concentration. The tests were carried out at 20°C and a pH of 7.79 - 8.44. Two endpoints were determined in the study: effects on parent mortality and effects on reproduction (number of offspring per adult). Parent mortality in the controls was 0 per cent in the test carried out with the 10 g/L nominal stock solution and 10 per cent in the test carried out with the 100 mg/L nominal stock solution.
      
   Elevated mortality was seen in the exposed populations. For the 10 g/L stock solution the LOEC was determined as the 1:8 dilution (approximately 58 - 65 μg/L) and the NOEC was determined as the 1:16 dilution (approximately 29 - 32 μg/L). For the 100 mg/L nominal stock solution the LOEC was determined as the 1:4 dilution and the NOEC was determined as the 1:8 dilution. These dilutions are based on the detection limit for the analysis of the 100 mg/L stock solution, and equate to LOEC and NOEC [values] of <5 and <2.5 μg/L respectively). From the dose response curves it appears that 100% parent mortality occurred at a concentrations of around <10 μg/L in the 100 mg/L nominal stock solution experiments and around 125 μg/L in the 10 g/L nominal stock solution experiments.
      
   For the reproduction endpoint, the average number of young per adult in controls was 72.3 in the 100 mg/L nominal stock solution series of experiments and 73.5 in the 10 g/L nominal stock solution experiments. A significant reduction in the number of young per adult was seen in some of the exposed organisms. For the 100 mg/L nominal stock solution, this effect on reproduction was significantly different from the control groups at the lowest concentration tested (a 1:16 dilution which is equivalent to a chlorinated paraffin concentration of <1.2 μg/L, based on the detection limit of the analytical method used). Thus the NOEC/LOEC for this series of experiments was <1.2 μg/L. Similarly, for the 10 g/L nominal stock solution effects were again seen at the lowest concentration tested (a 1:64 dilution, which is equivalent to a chlorinated paraffin concentration of 7.3 - 8.1 μg/L). This value is treated as the LOEC for this series of experiments. The report also indicates that the NOEC is very close to this value, since using a different statistical method (Dunnett's Test rather than Williams' Test), the effects seen at this concentration were not statistically significantly different from controls.

                  EPA/OPPT Conclusions
                  The interpretation of the results is complicated by the difficulties interpreting the effects from the different loading and dilution concentrations used. The actual exposure concentration in the 100 mg/L nominal stock solution is unknown and the measured concentration in the 10 g/L nominal stock solution (500 ug/L) is above the reported (estimated) water solubility of LCCPs. It was also noted in the U.K. environmental risk assessment, that the data for the 10 g/L loading were reanalyzed by Thompson (2001). The reanalysis suggests that the statistical significance of parent mortality is questionable and that the 1:8 dilution (20% mortality) considered as the LOEC is a marginal effect at best. The NOEC for parent mortality could be considered to be the 1:8 dilution (0.058  -  0.065 mg/L). In addition, there was a serious error found by Thompson (2001) in the statistical method. They determined that the statistical software misinterpreted increasing dilutions as increasing concentrations based on how the data were entered. Re-analysis of the data showed that effects were statistically significant compared with the controls only at the 1:8 dilution, leading to a NOEC at the 1:16 dilution (0.029  -  0.032 mg/L). This problem with the statistical analysis may also explain why the NOEC and LOEC from the 100 mg/L stock were observed below the lowest concentration tested; thus, the NOEC/LOEC of < 0.0012 mg/L is questionable. The data from these studies should be approached with caution due to deficiencies and uncertainties with the statistical analysis. The NOEC and LOEC values that follow are questionable.
                  21-day NOEC = 0.029  -  0.032 mg/L (10 g/L solution; parent mortality)
                  21-day LOEC = 0.058  -  0.065 mg/L (10 g/L solution; parent mortality)
                  21-day NOEC < 0.0025 mg/L (below detection limit; 100 mg/L solution; parent mortality)
                  21-day LOEC <= 0.0050 mg/L (below detection limit; 100 mg/L solution; parent mortality)
                  21-day NOEC < 0.0073 mg/L (10 mg/L solution; reproduction)
                  21-day LOEC <= 0.0073 mg/L (10 mg/L solution; reproduction)
                  21-day NOEC < 0.0012 mg/L (100 mg/L solution; reproduction)
                  21-day LOEC <= 0.0012 mg/L (100 mg/L solution; reproduction)

(2) TNO 1993
The test was carried out according to the OECD [211] methodology using a semi-static test procedure (test solution renewal was carried out every 48 - 72 hours). The test substance was identified as C18-20 chlorinated paraffin with 52% chlorination (Chloroparaffin Hoechst 56 Flüssig, Chloroparaffin Hoechst 52 Flüssig, and Hordaflex LC50. The dilution water used was a synthetic medium (DSWL) prepared by the addition of various salts to ground water. The hardness of the medium was 214 mg/L as CaCO3. The test was carried out using saturated solutions of the chlorinated paraffin using a column technique. The column was prepared by firstly dissolving/suspending 0.1 g of the test substance in 25 mL of acetone. This solution was then added to 10 g of the packing material for the column (chromosorb 60/80 mesh) and the acetone removed by rotation evaporation. The coated packing material was stored at room temperature in the dark until needed. The columns were stainless steel (25 cm long with an internal diameter of 4.3 mm) filled with 1 g of the coated packing material. The column was conditioned by pumping dilution water through at a flow rate of 6.2 mL every three minutes; the first 500 mL was collected and discarded. Around 18 litres of dilution water was then collected in a bottle and continually re-circulated through the column at a flow rate of 3.4 mL per minute throughout the test. The required amount of the saturated solution needed for the start of the test, and at each renewal period, was then taken from the bottle. 

Four replicates (10 daphnids in 400 mL of test solution) were carried out for each treatment. The tests were performed in 600 mL beakers and these were conditioned to the test solutions for two days prior to the start of the test. The solutions were renewed every Monday, Wednesday and Friday during the test. 

The concentration of test substance was determined at each renewal time in both the "fresh" solution and the "spent" solution. The analytical method used was based on extractable organic halogen (EOX; similar in principle to AOX) analysis. The mean EOX measured in the test solution over the course of the test was around 1 μg/L (the range found in the "fresh" solutions was 1.0 - 1.5 μg/L and the range in the "spent" solutions was 0.5 - 1.5 μg/L. The EOX concentrations in the control solutions were generally <0.5 μg/L in the "fresh" solution but the range found in the spent solutions was <0.5 - 1.0 μg/L for the blank control and 0.5 2.0 μg/L for the column control. 
      
The temperature, DO, and pH during the test were 19.2 - 20.3 ºC, >=7.1 mg/L and 7.6 - 8.5, respectively. The parent survival in both of the control groups was 97.5%. In the C18 - 20, 52% wt. Cl treatment group the parent survival was 92.5%. This survival was not significantly different (at the p=0.05 level) from the control group. Therefore, it was concluded that no treatment related effects on parent morality were seen in the study. The reproduction rate (expressed as the cumulative number of young per living female) in the study was 113.6 in the blank control and 127.3 in the column control. The response of the two controls was not significantly different (at the p=0.05 level). The reproduction rate in the C18 - 20, 52% wt. Cl treatment group was 100.8. This was 88.7 per cent of the blank control response and 79.1 per cent of the column control response. These responses were analyzed statistically in TNO (1993) using the two-tailed Dunnett-test. No statistically significant differences were found between the C18 - 20, 52% wt. Cl treatment group and the blank control, or the column control. 
      
                  EPA/OPPT Conclusions
                  Thompson (2007) conducted a further analysis of the results, due to the author's perception of discrepancies in the UK's (2009) Environmental Risk Assessment. The discrepancy was based on a seemingly contradictory statement from pg. 7 of the TNO report where the reproduction rate of the Hodaflex LC50 and Hoechst 52 Flüssig was stated as being significantly different from the controls (Pg.7 of the report) but not significantly different from the controls (Pg. 16 of the report). The data were re-analyzed by Thompson (2007) and no differences in the reproduction rate were observed between the C18-20, 52 wt% chlorination treatment groups Hodaflex LC50 and Hoechst 52 Flüssig, the column control, blank control or the pooled control group (combined blank control and column control). An additional statistical analysis was conducted by OPPT and no differences were determined for reproduction rate in the treatment groups versus controls using SAS (v. 9.3). Regardless of the discrepancy in the TNO report, statistically significant differences were reported by Thompson (2007) for adult mortality, reproduction rate, and mortality in general for Daphnia exposed to Hoechst 52 Flüssig compared to both controls. However, it is still unclear as to the levels of saturation of each solution the organisms were exposed to based on the extraction technique and nominal loading rates. Therefore, EPA/OPPT will reserve judgment on the acceptability of this study based on a weight of evidence approach. 
                  21-day NOEC = 0.002 mg/L (reproduction Hoechst 56 Flüssig)
                  

 Chronic Aquatic Sediment Invertebrate Toxicity
No data are available. Data from secondary sources using medium-chain chlorinated paraffins for chronic aquatic sediment invertebrate toxicity can be used to fill data gaps for the long-chain chlorinated paraffin; and these data were described above in the MCCP section.

 Avian Toxicity
No data are available. Data from secondary sources using medium-chain chlorinated paraffins for avian toxicity can be used to fill data gaps for the long-chain chlorinated paraffins; and these data were described above in the MCCP section.
  
 Terrestrial Invertebrate Toxicity
No data are available. Data from secondary sources using medium-chain chlorinated paraffins for terrestrial invertebrate toxicity can be used to fill data gaps for the long-chain chlorinated paraffins; and these data were described above in the MCCP section.

 Terrestrial Plant Toxicity
No data are available. Data from secondary sources using medium-chain chlorinated paraffins for terrestrial plant toxicity can be used to fill data gaps for the long-chain chlorinated paraffins; and these data were described above in the MCCP section.

 Conclusions 
Sufficient data were available to characterize the acute fish, the acute aquatic invertebrate, the chronic aquatic invertebrate, the chronic aquatic sediment invertebrate, avian, and terrestrial plant toxicity endpoints for MCCPs and LCCPs by read across in some instances. Data for other toxicity endpoints (i.e., chronic fish, aquatic plant, etc.) were inconclusive due to lack of study details, uncertainties in analytical methods, or test material preparation methods; thus, these data are included in order to characterize risk in a qualitative manner, but are used as supportive for the categories under which they are provided. Supporting data were included in order to provide a weight-of-evidence approach used to characterize some endpoints. 

Most of the data provided in this review indicated several difficulties were encountered when testing in an aquatic environment. These included: (1) getting the material into solution, (2) measuring the material in solution, and (3) characterizing the effects for each study listed. Often there were many details of a given study omitted, prohibiting a full and robust review of the data. The (estimated) physical-chemical properties of LCCPs and MCCPs (water solubility values between 2 and 30 μg/L and Log Kow values between 4-8) suggest these materials may not partition to the aquatic media or elicit toxicity to aquatic organisms within the water column. 

Specifically for the chronic and acute aquatic invertebrate, aquatic sediment, avian, and terrestrial plant endpoints for LCCPs, other analog data provided was acceptable using compounds with chlorination percentage of 52 wt% and carbon chain lengths of C14-17 which is defined as a MCCP material. These data are used in this assessment to fill data gaps for the C18-20 LCCPs as this would be a conservative approach to charactering hazard in the absence of data. Concern concentrations based on these data are again a very conservative approach in the absence of data for the LCCP materials themselves and therefore may not inherently characterize toxicity to LCCPs directly.

The most reliable and acceptable studies indicate that for MCCPs, the toxicity to aquatic organisms for acute endpoints are from the Thompson et al. 1996 study for aquatic invertebrates. Where the 48-hour EC50 value = 0.0059 mg/L. Using the methods described in the Sustainable Futures/P2 Manual (US EPA, 2012), the acute and chronic concentrations of concern (CoC) are derived as follows:

 Acute CoC: The 48-hour EC50 value = 0.0059 mg/L is divided by an assessment factor of 5 to yield an acute concentration of concern (CoC) of 0.00118 mg/L, or 0.001 mg/L, or 1 μg/L (1 ppb). Aquatic Acute Concern Concentration= 1 ppb
 Chronic CoC: The aquatic invertebrate chronic value of 0.013 mg/L from the 1997 Thompson et al. study based on a MCCP material is divided by an assessment factor of 10 to yield 0.0013 mg/L or 1.3 μg/L or 1.3 ppb. Aquatic Chronic Concern Concentration = 1 ppb

For LCCPs, the acute concern concentration may be derived from the Johnson and Finely (1980) studies. For the chronic concern concentration, the results from the Thompson et al. 1997 study based on a MCCP material will be used as a conservative qualitative assessment due to the lack of overly reliable data for this endpoint for LCCPs.

 Acute CoC: Aquatic Acute Concern Concentration= NES
 Chronic CoC: The aquatic invertebrate chronic value of 0.013 mg/L from the 1997 Thompson et al. study based on a MCCP material is divided by an assessment factor of 10 to yield 0.0013 mg/L or 1.3 μg/L or 1.3 ppb. Aquatic Chronic Concern Concentration = 1 ppb (MCCP and LCCP)

The most reliable and acceptable value for the toxicity to aquatic sediment invertebrate organisms acute endpoint is based on the MCCP material from the Thompson et al. 2002 28-d study. For both MCCPs and LCCPs, the 28-d sediment invertebrate GMATC value of 187 mg/kg dry wt sediment is used to assess hazard. The 28-d sediment invertebrate GMATC value of 187 mg/kg dry wt sediment is used to assess hazard. Again, using methods in US EPA (2012): 

 Acute CoC: Calculating an acute concern concentration from the chronic value of 187 mg/kg dry wt. The 187 value is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,870 mg/kg dry wt. This value is then divided by an assessment factor of 5 to yield 374 mg/kg dry wt. Aquatic Sediment Acute Concern Concentration = 374 mg/kg dry wt sediment. (MCCP and LCCP)
 Chronic CoC: The 28-d sediment invertebrate GMATC of 187 mg/kg dry wt sediment is divided by an assessment factor of 10 to yield 18.7 mg/kg dry wt sediment. Aquatic Sediment Chronic Concern Concentration = 19 mg/kg dry wt sediment. (MCCP and LCCP)

The most reliable and acceptable value for the toxicity to terrestrial invertebrates acute endpoint is based on the MCCP material from the Thompson et al. 2001a study. For LCCPs, the 28-d terrestrial invertebrate GMATC value of 149 mg/kg dry wt sediment will be used as an analog approach to assess hazard. The 28-d terrestrial invertebrate GMATC value of 149 mg/kg dry wt sediment from this study will be used. Again, using methods in US EPA (2012): 

 Acute CoC: Calculating an acute concern concentration from the chronic value of149 mg/kg dry wt, this value is multiplied by an acute to chronic ratio for invertebrates (10) to yield 1,490 mg/kg dry wt. This value is then divided by an assessment factor of 5 to yield 298 mg/kg dry wt. Terrestrial Invertebrate Acute Concern Concentration = 298 mg/kg dry wt sediment. (MCCP and LCCP)
 Chronic CoC: The 28-d terrestrial invertebrate GMATC of 149 mg/kg dry wt is divided by an assessment factor of 10 to yield 14.9 mg/kg dry wt sediment. Terrestrial Invertebrate Chronic Concern Concentration = 15 mg/kg dry wt sediment. (MCCP and LCCP)

The most reliable and acceptable value for the toxicity to terrestrial plants is based on the MCCP material from the Thompson et al. 2001ab study. For LCCPs, the analog approach using the values from this study may be used. However, there is no OPPT guidance regarding assessing concern concentrations for terrestrial plants. 

 HUMAN HEALTH HAZARD STUDY SUMMARIES

 MCCP HEALTH DATA REVIEW

 Metabolism 
There is no information on inhalation absorption of MCCPs in humans or in animals. Based on their low vapor pressure and low water solubility, absorption following inhalation or dermal exposure is expected to be limited. An in vitro study using human skin showed that after 24 hours, approximately 0.7% of a C15 chlorinated paraffin was absorbed (Scott, 1984; cited in: ECB, 2008). Oral studies (IRDC, 1984, CXR, 2005; cited in: ECB, 2008) showed that approximately 50% of a single dose of [8-[14]C]-labeled C15 chlorinated paraffin (52 wt% Cl) was absorbed from the GI tract in rats. Excretion via feces was the major route of elimination of radiolabeled material. Elimination of radioactivity from body tissues occurred with an elimination half-life of approximately 2-5 days (liver and kidney) or approximately 2 weeks (adipose tissue). 

 Acute Toxicity
There is no information on the effects of a single exposure to MCCPs in humans. No deaths and only limited, non-specific clinical signs of toxicity resulting from exposure of rats to very high doses were observed in an acute oral toxicity study of MCCPs (C14-17, 51-60 wt% Cl); the LD50 was reported to be > 4,000 mg/kg bw (Birtley et al., 1980; cited in: IPCS, 1996). Though no acute toxicity data are available for MCCP by the inhalation or dermal route of exposure, the low acute toxicity data for SCCPs by these routes suggest that MCCPs are likely to have low acute inhalation and dermal toxicity.
                 
 Irritation and Sensitization
No signs of skin irritation were seen with MCCPs (C14-17, 45 wt% Cl), and only slight erythema on the shaved skin was reported in one rabbit at 24 hours exposed to MCCPs (C14-17, 40 wt% Cl) (Chater, 1978; cited in: ECB, 2008). A mild skin irritancy response was reported in one of nine unpublished skin irritation studies of MCCPs (C14-17, 51-60% Cl) in rats (Birtley et al., 1980; cited in: ECB, 2008). The material caused slight, transient eye irritation in rabbits (Birtley et al., 1980; Kuhnert et al., 1986; cited in: ECB, 2008).

No skin sensitization reactions were produced in guinea pig maximization tests conducted on MCCPs (C14-17, 40-45 wt% Cl) (Murmann, 1988; Chater, 1978; cited in: ECB, 2008). 
                 
 Repeated-dose Toxicity
There are a number of repeated dose toxicity studies (up to 90-days duration) of MCCPs (C14-17 40 wt% Cl or 52 wt% Cl) in rats by oral exposure (CXR, 2005; Poon et al., 1995; IRDC, 1984; Birtley et al., 1980; and Wyatt et al., 1997; cited in: ECB, 2008). Though the quality and reliability of these studies differs, the liver, kidney, and thyroid were consistently established as the target organs. A summary of the results from these studies is provided in Table 1.    
     
MCCPs caused an increase in liver weight in male rats at exposure levels of > 100 mg/kg-bw/day) and in female rats at exposure levels of > 32 mg/kg-bw/day. Liver enzyme induction was reported in male and female rats starting from 222 and 100 mg/kg-bw/day, respectively. Liver hypertrophy of trace to minimal severity was reported in male rats at dose levels of > 100 mg/kg-bw/day and higher. Collectively, these changes are likely to be related to an increase in metabolic demand as an adaptive response and to peroxisome proliferation, both of which are considered of no or limited toxicological significance to humans. Though Poon et al. (1995) reported various histopathological effects in the liver of male and female rats at dose levels > 36 mg/kg-bw/day, there are a number of deficiencies with this study, including the scoring and classification of histopathological findings and limited reporting of data, which preclude its utility in hazard evaluation. This conclusion is consistent with previous evaluations of this study (ECB, 2008). Further, despite the consistency of findings reported in the review article by Birtley et al. (1980) with other 90-day studies, these findings should be viewed cautiously because the original full study report is not available. Based on the available data, the studies by IRDC (1984) and CXR (2005) provide the most reliable data for identifying effect levels of MCCPs on the liver. For the purposes of this assessment, a NOAEL of 100 mg/kg-bw/day was chosen based on increases in absolute liver weight (i.e., 22-26%), liver hypertrophy of trace severity, and enzyme induction (i.e., 30% increase).   

Kidney effects have been reported in a number of studies, with effect levels typically being observed at the limit doses. MCCPs (C14-17 52 wt% Cl) caused significant increases (9-13%) in kidney weight at 222 mg/kg-bw/day (CXR, 2005; cited in: ECB, 2008), as well as "chronic nephritis" and tubular pigmentation in the kidney of female rats at 625 mg/kg-bw/day (IRDC, 1984, cited in: ECB, 2008). One study reported a dose-related increase in congestion starting at 32 mg/kg-bw/day; however, no information was provided on the incidence or severity of this effect (Birtley et al., 1980; cited in: ECB, 2008). An additional study reported minimal to mild hyaline-droplet like cytoplasmic inclusions, starting at > 0.4 mg/kg-bw/day in male rats. This effect is considered of limited relevance to humans. The authors also reported minimal dose-related increases with inner medullary tubular dilation at an incidence of 1/10, 4/10, and 8/10 female rats at 4, 42, and 420 mg/kg-bw/day, respectively (Poon et al., 1995; cited in: ECB, 2008). Though this effect is considered relevant to humans, the study suffers from a number of limitations, which preclude utilizing it for hazard evaluation. However, based on the incidence reported by the authors, the NOAEL of 42 mg/kg-bw/day for kidney effects is consistent with the NOAEL of 23 mg/kg-bw/day reported in the CXR (2005) study. Therefore, a NOAEL of 23 mg/kg-bw/day was chosen for the kidney, based on increases in organ weight at the next highest dose level. 
     
MCCPs (C14-17 52 wt% Cl) have been reported to cause minimal to mild adaptive histopathological changes in the thyroid (i.e., follicular cell hypertrophy and hyperplasia) in two studies in rats starting at 50 ppm (4 mg/kg-bw/day) and above (Poon et al., 1995; IRDC, 1985). Decreased T4 levels and increased TSH levels in the plasma were also seen at similar dose levels. As noted previously, these results have been drawn into question based on the scoring and classification for histopathology, the limited reporting of data, and the inconsistent findings from other more robust studies (ECB, 2008). Therefore, these studies will not be considered further for hazard identification. IRDC (1985) reported mild to moderate hypertrophy and hyperplasia in male rats at dose levels of > 10 mg/kg-bw/day and higher, whereas changes in absolute organ weights of male and female rats were not observed except at the limit dose of 625 mg/kg-bw/day (IRDC, 1985; cited in: ECB, 2008). The remaining studies that evaluated thyroid hormone levels identified a decrease in plasma free T3 in male rats, but not total T3 or free/total T4, and an increase in TSH in female rats at dose levels of 24.6 or 242 mg/kg-bw/day, respectively (CXR, 2005; cited in: ECB, 2008), or fluctuations in thyroid hormones in male or female rats at doses of > 312 mg/kg-bw/day or higher (Wyatt et al., 1997; cited in: ECB, 2008). There is evidence that the thyroid effects observed are attributable to stimulation of this organ arising from a negative feedback effect arising from plasma T4 depletion following increased excretion of this hormone. This depletion of plasma T4 results from the induction of hepatic UDPG-transferase, increased glucuronidation, and ultimately excretion of T4 following exposure to MCCPs. The pituitary responds to the decreased levels of T4 by releasing more TSH, which in turn leads to increased production of T4 by the thyroid. The continuous stimulation of the thyroid in response to the increased excretion of plasma T4 is predicted to ultimately give rise to hypertrophy and hyperplasia in this organ. Humans, unlike rodents, possess T4-globulin binding protein and are therefore less susceptible to plasma T4 depletion and hence any resultant thyroid stimulation. The thyroid effects observed in rats are not considered to be of relevance to chronic human health at relevant levels of exposure, although these changes may be relevant for assessing potential adverse outcomes during reproduction and development, as discussed under Section C-1-7 in this Appendix.

 Genotoxicity
MCCPs (C14-17 40-52 wt% Cl) are not mutagenic to bacteria. Three in vivo bone marrow studies also show that MCCPs are not clastogenic (cited in: ECB, 2008). Therefore, it may be concluded that MCCPs possess a low potential to cause genotoxic effects.
      
 Carcinogenicity
There is no information on the carcinogenicity of MCCPs; however, carcinogenicity studies on a SCCP and a vLCCP are available. These studies, along with the genotoxicity data on MCCPs, may be used to inform the carcinogenic potential of MCCPs. When administered by gavage, a SCCP (C12, 60 wt% Cl) caused increased incidences of liver tumors in male and female rats, kidney tumors in male rats, and thyroid tumors in female rats (NTP, 1986a). However, based on mechanistic considerations, these tumors are considered to be of little or no relevance to humans.  This conclusion is consistent with previous carcinogenicity evaluations (ECB, 2008). An increased incidence of malignant lymphoma in male mice was reported at the highest dose of 5,000 mg/kg-bw/day in carcinogenicity studies of a vLCCP (C23, 43 wt% Cl) in male and female rats and mice (NTP, 1986b). Because it is unlikely that MCCPs are genotoxic, and the fact that cancer was only observed at the highest dose, the EU (UK 2009) assumed that there was a threshold for this effect in the mice. In addition, there was no increased incidence of malignant lymphoma observed in the carcinogenicity study on an SCCP discussed above. Further, MCCPs are non-genotoxic. Therefore, it may be concluded that MCCPs are unlikely to pose a carcinogenic hazard to humans.

Table_Apx C-1: Summary of Results from 90-day Studies in Rats Administered MCCPs
                             Strain (sample size)
                        Test substance and dose levels
                                 Target organ
                                 Effect levels
F-344 
(10 rats/sex/group)[1]
C14-17, 52 wt% Cl

Dietary intake for ♂: 0, 2.38, 9.34, 23.0, or 222 mg/kg-bw/day.

Dietary intake for ♀: 0, 2.51, 9.70, 24.6, or 242 mg/kg-bw/day.
Liver
♂ at 222 and ♀ at 242 mg/kg-bw/day, 13-31% ↑ in organ weight

♂ at 222 mg/kg-bw/day, minimal centrilobular hypertrophy  in 9/10 animals

♂ at 222 mg/kg-bw/day, 82% ↑ in microsomal T4-UDPGA-glucuronyl transferase activity

♀ at 100, 300, and 300 mg/kg-bw/day, 30, 30, and 252% ↑ in microsomal T4-UDPGA-glucuronyl transferase activity, respectively

Kidney
♂ at 222 and ♀ at 242 mg/kg-bw/day, 9-13% ↓ in organ weight

♂ at > 222 and ♀ at 242 mg/kg-bw/day, no treatment-related histopathology

Thyroid
♂ at 222 mg/kg-bw/day, 17% ↑  in plasma TSH

♂ at 23.0 and 222 mg/kg-bw/day, 26% or 22% ↓ in plasma free T3, respectively, but no effects on total T3 or on free/total T4 at any dose

♀ at > 242 mg/kg-bw/day, no effects on free/total T3 or T4

♀at 24.6 and 242 mg/kg-bw/day, 20 and 39% ↑  in plasma TSH

♂at > 222 and ♀ at 242 mg/kg-bw/day, no treatment-related histopathology
Sprague-Dawley 
(10 rats/sex/group)[2]
C14-17, 52 wt% Cl

Dietary intake for ♂: 0, 0.4, 4, 36, or 360 mg/kg-bw/day.

Dietary intake for ♀: 0, 0.4, 4, 42, or 420 mg/kg-bw/day.
Liver
♂ at 360 and ♀ at 420 mg/kg-bw/day, 28 and 48% ↑ in absolute and relative weights, respectively

♂ and ♀ at < 4 mg/kg-bw/day, no treatment-related histopathology

♂at 36 and ♀ at 42  mg/kg-bw/day, minimal increase in anisokaryosis and vesiculation of the nuclei

♂ at 360 and ♀ at 420 mg/kg-bw/day, mild increase in anisokaryosis and vesiculation of the nuclei (7-10 animals)

♂ at 360  mg/kg-bw/day, ↑ in perivenous homogeneity

♀ at 42 and 420 mg/kg-bw/day, ↑ in perivenous homogeneity

♂ at 360  and ♀ at 420 mg/kg-bw/day, ↑ in single cell necrosis (incidence not reported)

Kidney
♂ at 360 and ♀ at 420 mg/kg-bw/day, 11% ↑ in absolute and relative weights

♂ at > 0.4 mg/kg-bw/day, minimal to mild hyaline-droplet like cytoplasmic inclusions, with significant accumulation at the limit dose

♀ at > 4 mg/kg-bw/day, minimal dose-related inner medullary tubular dilation seen in 0/10, 0/10, 1/10, 4/10, and 8/10 animals

Thyroid
♂ at 36 and 360 mg/kg-bw/day, minimal to mild morphological changes affecting the architecture (i.e., reduced follicle sizes and collapsed angularity) and the epithelium (i.e., increased height, cytoplasmic vacuolation, and nuclear vesiculation)

♀ at > 4 mg/kg-bw/day, minimal to mild morphological changes affecting the architecture (i.e., reduced follicle sizes and collapsed angularity) and the epithelium (i.e., increased height, cytoplasmic vacuolation, and nuclear vesiculation)
F-344 
(15 rats/sex/group)[3]
C14-17, 52 wt% Cl

Dietary intake for ♂ and ♀: 0, 10, 100, or 625 mg/kg-bw/day.

Liver
♂ and ♀ at 100 and 625 mg/kg-bw/day, 22-26% and 64-92% ↑ in absolute weight values, respectively

♂ at 100 and 625 mg/kg-bw/day, hypertrophy of trace severity seen in 1/15 and 13/15 animals, respectively

♀ at 625 mg/kg-bw/day, hypertrophy of trace severity seen in 13/15 animals

Kidney
♂ and ♀ at 625 mg/kg-bw/day, 18% ↑ in absolute weight values

♂ at > 10 mg/kg-bw/day, trace to mild nephritis seen in 1/15, 3/15, 4/15, and 10/15 animals

♀ at 625 mg/kg-bw/day, tubular pigmentation (9/14 animals)

Thyroid
♂ at 625 mg/kg-bw/day, 50% ↑ in absolute weight values

♂ at > 10 mg/kg-bw/day, mild to moderate hypertrophy observed in controls with a dose-dependent trend towards ↑ severity in treated animals

♂ at > 10 mg/kg-bw/day, trace to mild hyperplasia with a dose-dependent trend towards ↑ severity 

Adrenal
♂ and ♀ at 625 mg/kg-bw/day, 25% ↑ in absolute weight values
Wistar-derived
(24 rats/sex/group)[4]
C14-17, 52 wt% Cl, containing epoxidized vegetable oil as a stabilizer

Dietary intake for ♂: 0, 33, 167, or 333 mg/kg-bw/day.

Dietary intake for ♀: 0, 32, 160, or 320 mg/kg-bw/day.

Liver
♂ at 167 and 333 mg/kg-bw/day, 15 and 22% ↑ in relative weight values, respectively

♀ at 32, 160, and 320 mg/kg-bw/day, 11, 21, and 48% ↑ in relative weight values, respectively

♂ at 333 and ♀ at 320 mg/kg-bw/day, no histopathological abnormalities

♂ at > 33 and ♀ at > 32 mg/kg-bw/day, dose-related ↑ in proliferation of smooth endoplasmic reticulum (electron microscopy)

Kidney
♂ and ♀ at limit dose, 15% ↑ in relative weight

♂ and ♀, dose-related ↑ in congestion (incidence and severity not reported) 

♂ and ♀ at > limit dose, no histopathological abnormalities
F-344 
(10 rats/sex/group)[5]
C14-17, 40 wt% Cl

Oral gavage for ♂ and ♀: 0, 312, or 625 mg/kg-bw/day
Liver
♂ and ♀ at 312 and 625 mg/kg-bw/day, 37 and 72% ↑ in relative weight, respectively, (absolute weight and bodyweight not presented)

♂ and ♀, dose-related ↑ in centrilobular hypertrophy (incidence and severity not reported) 

♂ and ♀ at 312 and 625 mg/kg-bw/day, dose-related ↑ in β-oxidation from day 29 onwards (~2.7- and 3.3-fold ↑, respectively, at study termination)

♂ and ♀ at 312 and 625 mg/kg-bw/day, dose-related ↑ in UDPG-transferase activity from day 15 onwards (up to 100% ↑, respectively)

Thyroid
♂ and ♀ at 312 and 625 mg/kg-bw/day, ↓ in levels of free and plasma T3, which reached statistical significance on days 15 and 57

♂ at 312 and 625 mg/kg-bw/day, ↑ TSH up to 2-fold on day 8 only

♀ at 312 and 625 mg/kg-bw/day, T3 significantly ↑ by day 91

♀ at 312 and 625 mg/kg-bw/day, total plasma T4 significantly ↓ by up to 25% on day 57

♂ and ♀ at 312 and 625 mg/kg-bw/day, ↑ follicular cell hypertrophy throughout the study, and accompanied by follicular cell hyperplasia on days 55 and 91 (incidence and severity not reported)

♂ and ♀ at 312 and 625 mg/kg-bw/day, significantly ↑ replicative DNA synthesis on day 29, but not on day 91
[1] CXR (2005), cited in: ECB (2008).
[2] Poon et al. (1995), cited in: ECB (2008).
[3] IRDC (1984), cited in: ECB (2008).
[4] Birtley et al. (1980), cited in: ECB (2008); note, this study was only summarized in the review by Birtley et al. (1980). The underlying original study report was not available.
[5] Wyatt et al. (1997), cited in: ECB (2008).

 Developmental Reproductive Toxicity Review
A series of range-finding and definitive prenatal developmental and reproductive toxicity studies were conducted in rats and rabbits with medium-chain chlorinated paraffins (MCCPs). These studies were conducted between 1981 and 1986. They appear to be valid toxicity studies, conducted according to the standard methodologies available at the time. More recently, additional studies with MCCPs have been conducted in an attempt to determine the cause of hemorrhaging in the pups observed in a one-generation reproductive toxicity range-finding study. 

In several prenatal developmental toxicity studies with MCCPs conducted via gavage, no signs of maternal toxicity were seen at doses as high as 500 mg/kg-bw/day in rats and 100 mg/kg-bw/day in rabbits. Likewise, no signs of developmental toxicity were observed at doses as high as 5000 mg/kg-bw/day in rats and 100 mg/kg-bw/day in rabbits. 

Two reproductive toxicity studies with MCCPs in rats have been conducted. A one-generation reproductive toxicity range-finding study showed that administration of approximately 100 and 400 mg/kg-bw/day MCCPs via the diet had no effect on fertility or other reproductive parameters; however, internal hemorrhaging and deaths in pups were observed beginning from 74 mg/kg-bw/day (1000 ppm) up to approximately 400 mg/kg-bw/day (6250 ppm). These effects in the pups were not seen in a more recent definitive one-generation reproductive toxicity study with exposure to MCCPs for 11-12 weeks to doses as high as 100 mg/kg-bw/day (1200 ppm). Internal hemorrhaging was not seen in the adult animals in either of these studies at doses as high as 400 mg/kg-bw/day (6250 ppm), or in another study in non-pregnant female rats repeatedly exposed to doses as high as 1000 mg/kg-bw/day. However, when dams were exposed to approximately 500 mg/kg-bw/day (6250 ppm) MCCPs during cohabitation, gestation, and lactation, signs of hemorrhaging were observed in dams that died at the time of parturition. Taken together, the results of these studies suggest that newborns during lactation and pregnant females at the time of parturition are a potentially sensitive subpopulation. 

The UK Risk Assessment (February, 2008) did not use the LOAEL of 74 mg/kg-bw/day (1000 ppm) from the one-generation reproductive toxicity range-finder study as a point of departure because the pup deaths at that dose were not statistically significant. The study itself used a limited number of animals and was intended for dose range-finding purposes only and, more importantly, the pup deaths were not repeated in a more recently conducted definitive study. With respect to developmental/reproductive toxicity, the UK Risk Assessment identified two subpopulations at risk: offspring during lactation and pregnant dams at parturition. The NOAELs from the definitive one-generation reproductive toxicity study (a maternal NOAEL ~ 47 mg/kg-bw/day (600 ppm) for effects on the offspring mediated via lactation; and a maternal NOAEL ~ 100 mg/kg-bw/day (1200 ppm) for effects on the dam during the time of parturition) were used to calculate risk. Assuming a conservative value of 50% oral absorption, the margin of safety (MOS) for effects on the offspring mediated via lactation and effects on the dam during the time of parturition were calculated for workers, consumers, and other scenarios. In all but one scenario (oil-based metal working fluids), the margins of safety were above 100 and in many cases, several fold above. In addition, margins of exposure were calculated for infants exposed via breast milk and via cow's milk, and in both instances, large MOEs (i.e., > 100) were calculated.             

Additional studies with MCCPs have been conducted in an effort to clarify the possible causes of the hemorrhaging in the pups. One (single-dose; 6250 ppm or 538 mg/kg-bw/day) study showed maternal death during parturition due to low levels of vitamin K and related hemorrhaging, suggesting that the act of parturition places dams at higher risk. It was concluded in data from this study and a cross-fostering study that the fetus relies on clotting factors via mother's milk and severe deficiencies in vitamin K levels and related clotting factors in the pups results in hemorrhaging.   

No definitive developmental neurotoxicity studies on MCCPs were located. It is not clear if any developmental neurotoxicity endpoints were actually measured in the available prenatal developmental/reproductive toxicity studies; none were explicitly stated. The only information available regarding behavior during development is from cage-side observations in pups through LD 21. In these cases, no dose-related differences were reported in F1 post-weaning appearance or cage-side behaviors. 

In the prenatal developmental toxicity study in rats, the LOAEL for maternal toxicity was 2000 mg/kg-bw/day based on clinical signs. The NOAEL for maternal toxicity was 500 mg/kg/day. The NOAEL for developmental toxicity was 5000 mg/kg-bw/day, the highest dose tested.     

In the prenatal developmental toxicity study in rabbits, no adverse, treatment-related effects were reported in the dams or the offspring. The NOAEL for both maternal and developmental toxicity was 100 mg/kg-bw/day, the highest dose tested.     

In the reproduction range-finding study in rats (IRDC, 1981, cited in ECB, 2008), the LOAEL for maternal toxicity was 6250 ppm (463 mg/kg-bw/day) based on reductions in body weight gains. The NOAEL for maternal toxicity was 1000 ppm (74 mg/kg-bw/day). The LOAEL for developmental toxicity was 1000 ppm (62/74 mg/kg/day) based on pup mortality associated with internal hemorrhages. The NOAEL for developmental toxicity was 100 ppm (6/8 mg/kg-bw/day). No effects on any reproductive parameters were reported. The NOAEL for reproductive toxicity was 6250 ppm (384/463 mg/kg-bw/day). 

In the one-generation reproduction toxicity study in rats, the LOAEL for maternal toxicity was 1200 ppm (~100 mg/kg-bw/day) based on increases in liver weight; the NOAEL for maternal toxicity was 600 ppm (~ 47 mg/kg-bw/day). The NOAEL for developmental and reproductive toxicity was 1200 ppm (~ 84/99 mg/kg-bw/day), the highest dose tested.     

Basis for Conclusions 
  
In a range-finding prenatal developmental toxicity study in pregnant Charles River COBS CD rats administered MCCPs (C14-17, 52 wt% Cl) via gavage at dose levels of 0, 1000, 1500, and 2500 mg/kg-bw/day on gestation days (GD) 6-20, no effects were observed in the dams at doses up to 2500 mg/kg-bw/day (IRDC, 1983, 1984; cited in: ECB, 2008). As a result, doses greater than 2500 mg/kg-bw/day were selected for the definitive study. 
   
In the definitive study, four groups of 25 pregnant Charles River COBS CD rats were administered MCCPs (C14-17, 52 wt% Cl) via gavage at doses of 0, 500, 2000, and 5000 mg/kg-bw/day on GD 6-19 (IRDC, 1984; cited in: ECB, 2008). Unmated males and females were individually housed and acclimated for 21-days in an environmentally controlled room. At the end of the acclimation period, all animals were weighed and subjected to a detailed physical examination. One female and one male rat were placed together for mating. Confirmation of mating was based on evidence of a copulatory plug or by vaginal smear for sperm. The day mating was confirmed was designated as day 0 of gestation. Test article was administered to pregnant females orally by gavage as a single daily dose on GD 6-19. During treatment, pregnant females were observed daily for mortality and clinical signs of toxicity. Any females not surviving to scheduled sacrifice were necropsied. Body weights were recorded on GD 0, 6, 9, 12, 16, and 20. All females were sacrificed on GD 20 and the uterus and ovaries excised for examination. The number and location of viable and nonviable fetuses, early and late resorptions, and the number of total implantations and corpora lutea were recorded. The uterus was weighed. The abdominal and thoracic cavities underwent gross examination. Maternal tissues were preserved for future histopathological analysis. Fetuses were weighed, sexed, tagged, and examined for external malformations and variations, including the palate and the eyes. The fetuses underwent visceral and skeletal examinations for malformations and developmental variations.     
      
The only effects reported in dams consisted of an increased incidence in wet matted and yellow stained haircoat in the anogenital area at 5000 mg/kg-bw/day, and soft stool at > 2000 mg/kg-bw/day. No treatment-related adverse effects were reported in offspring at doses up to 5000 mg/kg-bw/day. The LOAEL for maternal toxicity was 2000 mg/kg-bw/day based on clinical signs; the NOAEL for maternal toxicity was 500 mg/kg-bw/day. The NOAEL for developmental toxicity was 5000 mg/kg-bw/day, the highest dose tested.   
      
In a range-finding prenatal developmental toxicity study in pregnant Dutch Belted rabbits administered MCCPs (C14-17, 52 wt% Cl) via gavage at dose levels of 0, 100, 300, 1000, 2000, and 3000 mg/kg/day on GD 6-27, an increase in the number of abortions was observed at > 1000 mg/kg/day (IRDC, 1985; cited in: ECB, 2008). Body weight reductions in the dams were reported at 100 and 300 mg/kg/day. As a result, another range-finding prenatal developmental toxicity study in rabbits was initiated. This second range-finding study showed decreases in maternal weight gain at 80 and 160 mg/kg-bw/day (IRDC, 1982b; cited in: ECB, 2008). 
   
Based on the results of these range-finding studies, dose levels of 10, 30, and 100 mg/kg-bw/day were selected for the definitive prenatal oral gavage developmental toxicity study (IRDC, 1983; cited in: ECB, 2008). In the definitive study, four groups of 16 pregnant Dutch Belted rabbits were administered 0, 10, 30, and 100 mg/kg-bw/day MCCPs (C14-17, 52 wt% Cl) via gavage on GD 6-27. Unmated males and females were individually housed and acclimated for 50-days in an environmentally controlled room. As a result of a positive finding for parasites in stool samples collected during acclimation, all rabbits received sodium sulfamethazine in their drinking water for 16 days during the acclimation period. This treatment was terminated 4 weeks prior to study initiation and only rabbits testing negative for parasites were placed on study. At the end of the acclimation period, all animals were weighed and subjected to a detailed examination. Females were impregnated via artificial insemination. Three weeks prior to artificial insemination, females were given chorionic gonadotropin via an injection in a marginal ear vein in order to induce superovulation. Semen was collected from males of proven fertility and evaluated for motility. The day of artificial insemination was designated as day 0 of gestation. During treatment, pregnant females were observed for mortality and clinical signs of toxicity. Body weights were recorded on GD 0, 6, 12, 18, 24, and 28. Any females not surviving to scheduled sacrifice were necropsied. On GD 28, all surviving females were sacrificed and the uterus and ovaries excised for examination. The location and number of viable and nonviable fetuses, early and late resorptions, and the number of total implantations and corpora lutea were recorded. The uterus was weighed. The thoracic and abdominal cavities underwent gross examination. Pooled samples of abdominal adipose tissue from 3 dams were frozen for future analysis. Each fetus was sexed, weighed, and examined for external malformations and variations, including the palate and the eyes, as well as visceral and skeletal examinations for malformations and developmental variations, including examination of the brain and the heart.
      
No adverse, treatment-related effects were reported in the dams or the offspring at doses up to 100 mg/kg-bw/day. The NOAEL for both maternal and developmental toxicity was 100 mg/kg-bw/day, the highest dose tested.     

In a one-generation reproductive toxicity range-finding study, four groups of 5 male and 10 female Charles River COBS SC rats were administered MCCP (C14-17, 52 wt% Cl) via the diet at 0, 100, 1000, and 6250 ppm (~ 0, 6, 62, and 384 mg/kg-bw/day, respectively, in males; and 0, 8, 74, or 463 mg/kg-bw/day, respectively, in females) (IRDC, 1985; cited in: ECB, 2008). F0 animals were exposed to test substance from 28 days prior to mating until sacrifice; F1 animals were treated from weaning until sacrifice, with additional potential exposures occurring in utero and during lactation. All F0 males were sacrificed after the mating period. Following the premating period, each male was cohabited with two females for 10 days. Females were examined for evidence of copulation by means of vaginal smears and/or the appearance of a vaginal plug. The day evidence of copulation was determined was designated as day 0 of gestation. Direct dosing began at 83 days of age for the F0 parents and at 21 days of age for the F1 weanlings. The F0 and F1 animals were observed for clinical signs of toxicity, changes in general appearance and behavior, and mortality. In the F0 adults, body weights and food consumption were measured weekly; in addition, body weights were measured in F0 females on GD 0, 7, 14, and 20; and on lactation days (LD) 0, 7, 14, and 21. Estrous cyclicity was determined in F0 females prior to mating, during mating, and prior to dosing. All F0 females were allowed to deliver. The day the entire litter was found and delivery was judged to be complete was designated as LD 0. Gestation duration was calculated. Following delivery, all pups were examined for external malformations and the numbers of live births and stillbirths (litter size) was recorded for each dam. Pups were weighed, sexed, and examined externally on LD 0, 7, 14, and 21. Litter size was determined on LD 0, 4, 10, and 21. The number of male and female pups was recorded on LD 4. Litters were examined daily for survival. F0 females were examined for behaviors in nesting and nursing. On LD 21, all dams were sacrificed and a gross necropsy performed, including examination of the uterine contents for implantation sites; and ten F1 weanlings/sex/dose were sacrificed and necropsied. Five F1 males and ten F1 females/dose group were retained after LD 21 and sacrificed at 70 days (10 weeks) of age and necropsied. Due to high mortality in high-dose F1 pups, the surviving F1 pups in the high-dose group and an equal number of control pups were sacrificed on LD 6 and 7 and necropsied. Blood was collected via heart puncture and complete blood counts performed. Bone marrow smears were collected from the femur, and the abdominal contents of the pups with milk in the stomach were collected and frozen for future analyses. 
   
Effects in the adults consisted of isolated reductions food consumption and body weight in the dams at 6250 ppm. Effects in the offspring consisted of significant reductions in pup survival at the high dose (none of the F1 pups in the high-dose group survived until lactation day 21); and slight (11%, not statistically significant) decreases in pup survival, and labored breathing, subcutaneous hematoma, pale discoloration, blood around the orifices, pale liver, kidney, and spleen, and blood in the cranial cavity and brain beginning at the mid-dose. No dose-response, treatment-related adverse effects were reported in the offspring in the low dose group. Reductions in body weight in F1 male and female pups occurred during LD 7, 14, and 21, but these reductions were not statistically significantly different from controls, and were seen only in the low- and mid-dose groups but not the high-dose group. There were no dose-related differences in F1 post-weaning appearance, behavior, food consumption, or clinical or anatomical pathology in the low- and mid-dose groups. Based on the results of this study, it was recommended that dosage levels in a two-generation reproduction toxicity study not exceed 1000 ppm. The LOAEL for maternal toxicity was 6250 ppm (~463 mg/kg-bw/day) based on reductions in body weight gains. The NOAEL for maternal toxicity was 1000 ppm (~74 mg/kg-bw/day). The LOAEL for developmental toxicity was 1000 ppm (~62/74 mg/kg-bw/day) based on pup mortality due to hemorrhaging. The NOAEL for developmental toxicity was 100 ppm (~6/8 mg/kg-bw/day). No effects on any of the reproductive parameters were reported. The NOAEL for reproductive toxicity was 6250 ppm (~384/463 mg/kg-bw/day). 

In an effort to determine the cause of hemorrhaging in the pups at the high dose from the reproductive toxicity range-finding study, a screening level cross-fostering developmental toxicity study was conducted in Charles River COBS Wistar rats fed diets containing either 0 or 6250 ppm (~ 3125 mg/kg-bw/day) MCCPs (C14-17, 52 wt% Cl) for 4 weeks prior to mating and throughout pregnancy in a series of groups (Hart et al., 1985; cited in: ECB, 2008). Offspring from two of these groups (pups from control females reared from treated females, and pups reared from their treated mothers) showed high-pup mortality associated with internal hemorrhages. Hematological assays in the pups from these two groups showed decreases in factor X, resulting in a disruption of a vitamin K-dependent clotting system (lower plasma vitamin K levels). It was concluded that the pup mortalities were due to internal hemorrhages caused by a decrease in the vitamin K-dependent hemostatic mechanism (not examined in this study), induced during lactational exposures via the milk from mothers receiving MCCPs. 

Additional studies have been conducted to investigate two hypotheses in an effort to clarify the possible causes of the hemorrhaging in the pups. 

The first hypothesis proposes that MCCPs induce a catabolism of vitamin K in lactating rats leading to decreased plasma concentrations and ultimately low levels of vitamin K in the milk pups receive (vitamin K controls the formation of several clotting factors in the liver). In order to test this hypothesis, a preliminary study (CXR Biosciences Ltd., 2003; cited in: ECB, 2008) was conducted in which three groups of 6 female adult Sprague-Dawley were administered MCCPs (C14-17, 52 wt% Cl) via gavage at doses of 0, 500, or 1000 mg/kg-bw/day for 21 days while being fed a normal diet or a vitamin K-deficient diet. Following exposures to MCCPs, significant decreases in plasma concentrations of a clotting factor were seen in rats fed a normal diet; however, these decreases did not affect prothrombin clotting times. Reductions of a clotting factor in both treated and control groups were also seen in animals fed a vitamin-K deficient diet. Plasma vitamin K levels were not affected by treatment in the normal diets, but they were lower in high-dose animals fed vitamin K-deficient diets. The results from this study suggested that MCCPs did not adversely affect the blood clotting system in adult female rats treated for 3 weeks up to a dose of 1000 mg/kg-bw/day; and the hemorrhaging effects in pups are unlikely to be mediated by reduced vitamin K levels in breast milk.                

The second hypothesis proposes that MCCPs transferred to the pups through breast milk causes disruption of the pup clotting system. In order to test this hypothesis, a study (CXR Biosciences Ltd., 2004; cited in: ECB, 2008) was conducted in two groups of 16 male and 32 female Sprague-Dawley rats administered 0 or 6250 ppm (~ 0 and 513 and 538 mg/kg-bw/day in males and females, respectively) MCCPs (C14-17, 52 wt% Cl) for 4 weeks prior to mating, during cohabitation, gestation, and lactation until study termination (at about 2 weeks after the first litters were born, due to high rate of pup mortality). Milk, blood, and liver samples from lactating dams, and blood and liver samples from lactating pups were assessed for plasma vitamin K levels. Five dams died or were killed at the time of parturition (16% mortality). These deaths were considered to be treatment-related as there was no indication of obstruction or hindrance to delivery. The clinical necropsy of these dams showed effects suggestive of hemorrhaging in 3 out of the 5 dams and one male who died. Slight reductions in food consumption and body weight gains were observed during gestation and lactation. There were no effects on mating performance or duration of gestation. Concentrations of plasma vitamin K levels in adult females having gone through lactation and pregnancy was markedly decreased by treatment with MCCPs, which in turn produced a decrease in activity of the plasma clotting factors in treated dams. Prothrombin clotting times were not affected in the dams, suggesting that the functional reserve in these adult animals was sufficient. Pup plasma volumes were reportedly insufficient to measure vitamin K directly, but clotting factor activities were possible to analyze. No effects on litter size at birth or on pup mortality from birth to LD 4 were reported; however, after pup mortality increased significantly after LD 4. The majority of these pups showed internal hemorrhages at necropsy. It was concluded that data from this study and the cross-fostering study performed by Hart et al. (1985) suggest that the fetus receives sufficient vitamin K via the placenta, but after birth becomes severely deficient in vitamin K and related clotting factors and relies on these factors via mother's milk. In addition, the pups also receive considerable levels of MCCPs via lactation (through mother's milk) which may also contribute to further reducing the vitamin K levels. These severe deficiencies in vitamin K levels and related clotting factors in the pups results in hemorrhaging. It was also concluded that the act of parturition places dams at higher risk.   

More recently, a definitive one-generation reproductive toxicity study was conducted to refine the NOAEL for effects in the offspring and to further explore the mechanisms of hemorrhaging (CXR, 2006; cited in: ECB, 2008). This study was reportedly conducted in compliance with OECD TG 421 and Good Laboratory Practice standards. Four groups of 12-17 male and female Sprague-Dawley rats were administered 0, 300, 600, and 1200 ppm (~ 0 and 21, 44, and 84 mg/kg-bw/day in males; and 0, 23, 47, and 99 mg/kg-bw/day in  females) MCCPs (C14-17, 52 wt% Cl) for 4 weeks prior to mating, during cohabitation, gestation, and lactation until study termination (for a total treatment of 11-12 weeks). Males were terminated on LD 4 (9 weeks of treatment) and females were allowed to litter and rear their offspring until PND 21. Females were sacrificed on LD 21. Adult males were assessed for signs of clinical toxicity, body weight, food consumption, and macropathology. Adult females were assessed for signs of clinical toxicity, body weight, food consumption, gestation length, parturition, liver weights, and macropathology. Mating performance and fertility were also evaluated. Offspring evaluations included clinical signs of toxicity, litter size, survival, sex ratio, body weight, and pathological examinations at necropsy. Milk, blood, and liver samples were obtained from selected offspring at specific time points between birth of litters and PND 21. In addition, blood, liver, and milk samples from a satellite group of five females and their litters from the control and high-dose group (1200 ppm) were collected for future analysis. Analysis of these samples was still pending at the time of the UK assessment. 

No adverse effects were reported in the adult animals for clinical condition, body weight, body weight gain, food consumption, estrous cycling, mating performance, pre-coital interval, fertility, number of implantations, gestation lengths, or parturition. The only effect reported was for higher absolute and relative liver weights in high-dose females (1200 ppm; 99 mg/kg-bw/day). Likewise, no adverse effects were in the offspring at any dose level for litter size, sex ratio, offspring survival, body weights, body weight gains, macropathology and liver weights. No adverse effects were reported on pre- and post-natal survival and growth up to sacrifice (weaning). Though no histopathology was performed, the body cavity and cranial cavity were opened and examined for any signs of hemorrhaging. None was reported. Based on the results of this study, the LOAEL for maternal toxicity was 1200 ppm (~100 mg/kg-bw/day) based on increases in liver weight; the NOAEL for maternal toxicity was 600 ppm (~ 47 mg/kg-bw/day). The NOAEL for developmental and reproductive toxicity was 1200 ppm (~ 84/99 mg/kg-bw/day), the highest dose tested. 

 LCCP HEALTH DATA REVIEW

P-12-0433 is a C18-20 LCCP. Much of the information presented here is based on data with vLCCPs (i.e., carbon chain lengths of >C20).
 
The National Research Council (NRC, 2000) reviewed the toxicological risks of selected flame retardant, including a LCCP containing C24 with 70 wt% Cl. Based on the NOAEL of 900 mg/kg-bw/day (liver toxicity), the NRC derived an RfD of 0.3 mg/kg-bw/day. Using this RfD and the worst case average daily exposure to be 0.16 mg/kg/day, NRC concluded: "LCCP do not pose a noncancer risk when incorporated into residential furniture at the estimated application levels." Further, it was concluded that: "LCCP are not likely to be a human carcinogen and derivation of a cancer potency factor is unnecessary."
 
 Metabolism 
There is no information on inhalation absorption of LCCPs in humans or in animals. Based on their low vapor pressure and low water solubility, absorption following inhalation or dermal exposure is expected to be limited.
Oral (gavage) studies (IRDC, 1981; cited in: UK, 2009) showed that approximately 82-95% of a single dose of [8-[14]C]-labeled C22-26 chlorinated paraffin (43% Cl) was recovered in the feces in rats during the seven-day collection period. Only 0.1-0.8% of the radiolabel was excreted in the urine. For C22-26 chlorinated paraffin (70 wt% Cl), it was found that 61-88% of the administrated radioactivity was recovered in the feces in rats during the seven-day collection period. Less than 0.1-1% was excreted in the urine.

 Acute Toxicity
Acute toxicity studies have been conducted in rats, mice or dogs on five LCCPs: C20-30 , 41-50 wt% Cl; C22-26, 42 wt% Cl, C23, 43 wt% Cl; C20-30, 61-70 wt% Cl; C24, 70% Cl. The maximum dose levels used in these studies ranged from 4-50 g/kg-bw. No deaths were reported in any of the studies (IUCLID, 2003; cited in: UK, 2009). 

 Irritation and Sensitization
Skin irritation testing has been conducted on four LCCPs: C19 ,44 wt% Cl; C22-26, 42 wt% Cl; C20-30, 41-50 wt% Cl; C20-30, 70 wt% Cl. No evidence of irritation was seen in three of the four LCCPs. For the C22-26, 42 wt% Cl product, erythema was observed in two of six animals tested; the severity threshold was below the classification of the EU system (IUCLID, 2003; cited in: UK, 2009).

Evidence of slight eye irritation was seen in a test of a C22-26, 42 wt% Cl product. However, the criteria for classification as an eye irritant were not met (IUCLID, 2003; cited in: UK, 2009).
         
In a maximization test and a Buehler test using guinea pig, a C22-26, 42 wt% Cl product was negative (IUCLID, 2003; Bailey and Sheldon, 1998; cited in: UK, 2009). A C18-27, 40 wt% Cl product was reported to elicit a positive response in the guinea pig maximization test (IUCLID, 2000; cited in: UK, 2009). However, no information is available on the quality of this study. 
                 
 Repeated-dose Toxicity
LCCPs with C20-30, 43 wt% Cl were dissolved in corn oil and given by gavage at 100, 900 or 3,750 mg/kg-bw/day to groups of 15 male and female Fisher 344 rats in a 14- and a 90-day studies (IRDC1981, 1984; cited in: Serront et al., 1987). There was a treatment-related effect on the liver of female rats at all dose levels, but no liver effects were seen in the males. Female liver weights were increased and a multifocal granulomatous hepatitis characterized by inflammatory changes and necrosis. Nephrosis was observed in the kidney of male rats and mineralization in the kidneys of female rats at 3,750 mg/kg-bw/day. Similar liver effects were observed in the high-dose (3,750 mg/kg-bw/day) rats of both sexes in a 90-day study on LCCPs with C22-26, 70 wt% Cl (IRDC1981; cited in: Serront et al., 1987) and in a 90-day study as well as a 2-year bioassay on a LCCP with an average of C23, 43 wt% Cl at 100 mg/kg-bw/day (NTP, 1986). Based on the liver toxicity, a LOAEL of 100 mg/kg-bw/day is established for the LCCPs with 43 wt% Cl and a NOAEL of 900 mg/kg-bw/day is identified for the LCCPs with 70 wt% Cl.		
 Genotoxicity
Both LCCPs of C22-26, 43 wt% Cl and C23, 43 wt% Cl were negative in several Salmonella strains of the Ames test with or without metabolic activation (IUCLID, 2003; NTP, 1986; cited in: UK, 2009). LCCPs with C20-30 with 43 wt% Cl or C22-26 with 70 wt% Cl did not induce significant increases of chromosomal or chromatid aberrations in bone marrow cells of rats (IRDC1983; cited in: Serrone et al., 1987). 
                 
 Carcinogenicity
The carcinogenicity of a vLCCP (C23, 43 wt% Cl) was studied by administering the chemical in corn oil by gavage to groups of 50 F344/N rats and 50 B6C3F1 mice of each sex, 5 days per week for 103 weeks (NTP, 1986). Male rats received doses of 0, 1,875 or 3,750 mg/kg-bw/day; female rats and mice received 0, 2,500 or 5,000 mg/kg-bw/day. An increased incidence of malignant lymphomas was reported for male mice given the LCCP; the incidences for the controls, low- and high dosed groups are 6/50, 12/50, and 16/50, respectively. vLCCPs are not genotoxic (see review in Appendix C, Section C-2-6), and the fact that cancer was only observed at the highest dose, the EU (UK 2009) assumed that there was a threshold for this effect in the mice. In addition, there was no increased incidence of malignant lymphoma observed in the carcinogenicity study on an SCCP (also discussed above in the MCCP section). It has been concluded that LCCPs are unlikely to pose a carcinogenic hazard to humans (NRC, 2000; Serrone et al., 1987). 
 Developmental Reproductive Toxicity Review
In a prenatal developmental toxicity study in rats, no treatment-related effects were reported. The NOAEL for both maternal and developmental toxicity was 5000 mg/kg-bw/day, the highest dose tested.   

In a prenatal developmental toxicity study in rabbits, the LOAEL for maternal toxicity was 500 mg/kg-bw/day (the lowest dose tested) based on increased incidence of clinical signs. The NOAEL for developmental toxicity was > 2000 mg/kg-bw/day, the highest dose tested.

In a prenatal developmental toxicity study in rabbits, the NOAEL for both maternal and developmental toxicity was 1000 mg/kg-bw/day, the highest dose tested. 

Basis for Conclusions 

In a range-finding study (Study # 438-033, October 27, 1981; Chlorinated Paraffin Consortium), in pregnant Charles River COBS rats administered LCCP (22-26 carbons, 43 wt% Cl) via gavage at dose levels of 0, 3000, and 5000 mg/kg-bw/day on GD 6-19, the only effects reported occurred in dams and consisted of a slight increased incidence in anogenital matting during the latter portion of the treatment period at 5000 mg/kg-bw/day. No adverse treatment-related effects were reported in offspring at doses up to 5000 mg/kg-bw/day. 

Based on the findings of the range-finding study, four groups of 25 pregnant Charles River COBS CD rats were administered LCCP (22-30 carbons, 70 wt% Cl) via gavage at doses of 0, 500, 2000, and 5000 mg/kg-bw/day on GD 6-19 (Study # 438-045, April 11, 1984; Chlorinated Paraffin Consortium). Unmated males and females were individually housed and acclimated for 15-days in an environmentally controlled room. At the end of the acclimation period, all animals were weighed and subjected to a detailed physical examination. One female and one male rat were placed together for mating. Confirmation of mating was based on evidence of a copulatory plug. The day mating was confirmed was designated as day 0 of gestation. Test article was administered to pregnant females orally by gavage as a single daily dose on GD 6-19. During treatment, pregnant females were observed daily for mortality and clinical signs of toxicity. Any females not surviving to scheduled sacrifice were necropsied. Body weights were recorded on GD 0, 6, 9, 12, 16, and 20. All females were sacrificed on GD 20 and the uterus and ovaries excised for examination. The number and location of viable and nonviable fetuses, early and late resorptions, and the number of total implantations and corpora lutea were recorded. The uterus was weighed. The abdominal and thoracic cavities underwent gross examination. Maternal tissues were preserved for future histopathological analysis. Fetuses were weighed, sexed, tagged and examined for external malformations and variations, including the palate and the eyes. The fetuses underwent visceral and skeletal examinations for malformations and developmental variations.     
        
No adverse treatment-related effects were reported in the dams or offspring at doses up to 5000 mg/kg-bw/day. The NOAEL for both maternal and developmental toxicity was 5000 mg/kg-bw/day, the highest dose tested.   

In a range-finding study (Study # 438-018, October 27, 1981; Chlorinated Paraffin Consortium) in pregnant Dutch Belted rabbits administered LCCP (22-26 carbons, 43 wt% Cl) via gavage at doses of 0, 500, 1000, 2000, 3000, and 5000 mg/kg-bw/day on GD 6-27, a slight decrease in the amount of feces and a slight increase in matting and/or staining of the haircoat was reported in the dams at > 3000 mg/kg-bw/day. No other effects were reported. Observations of offspring did not appear to be included.   

Based on the results of the range-finding study, four groups of 16 Dutch Belted pregnant rabbits were administered LCCP (22-26 carbons, 43 wt% Cl) via gavage at doses of 0, 500, 2000, and 5000 mg/kg-bw/day on GD 6-27 (Study # 438-030, August 26, 1982; Chlorinated Paraffin Consortium). Unmated males and females were individually housed and acclimated for 9-weeks in an environmentally controlled room. As a result of a positive finding for parasites in stool samples collected during acclimation, all rabbits received sodium sulfamethazine in their drinking water for 19 days during the acclimation period. This treatment was terminated 5 weeks prior to study initiation and only rabbits testing negative for parasites were placed on study. At the end of the acclimation period, all animals were weighed and subjected to a detailed examination. Females were impregnated via artificial insemination. Immediately after insemination, ovulation was induced via an injection of chorionic gonadotropin in a marginal ear vein. Semen was collected from males of proven fertility and evaluated for motility. The day of artificial insemination was designated as day 0 of gestation. During treatment, pregnant females were observed for mortality and clinical signs of toxicity. Body weights were recorded on GD 0, 6, 12, 18, 24, and 28. Any females not surviving to scheduled sacrifice were necropsied. On GD 28, all surviving females were sacrificed and the uterus and ovaries excised for examination. The location and number of viable and nonviable fetuses, early and late resorptions, and the number of total implantations and corpora lutea were recorded. The uterus was weighed. The thoracic and abdominal cavities underwent gross examination. Pooled samples of abdominal adipose tissue from 3 dams were frozen for future analysis. Each fetus was sexed, weighed, and examined for external malformations and variations, including the palate and the eyes, as well as visceral and skeletal examinations for malformations and developmental variations, including examination of the brain and the heart.

A dose-related trend in an increased incidence in soft stool and/or anogenital matting or staining was observed in the dams beginning at the low-dose group. Three dams aborted and were sacrificed during treatment; one in the mid-dose group, and two in the high-dose group. Increases in postimplantation loss and corresponding decreases in viable fetuses, and increases in late resorptions were reported at the high-dose group, however, these effects were not reported as being statistically significant.  No signs of treatment-related developmental toxicity were reported in the offspring at < 5000 mg/kg-bw/day, although the sample size in the high-dose group was limited, precluding any definitive conclusions. Therefore, the LOAEL for maternal toxicity was 500 mg/kg-bw/day (the lowest dose tested), based on increased incidence of clinical signs. The NOAEL for developmental toxicity was > 2000 mg/kg-bw/day.

In a range-finding study (Study # 438-038, November 1, 1982; Chlorinated Paraffin Consortium) in pregnant Dutch Belted rabbits administered LCCP (22-30 carbons, 70 wt% Cl) via gavage at doses of 0, 2000, 3750, and 5000 mg/kg-bw/day on GD 6-27, increases in abortions, reductions in maternal body weight, and increases in post-implantation losses were reported at > 2000 mg/kg-bw/day. Therefore, a second range-finding study was conducted at dose levels of 0, 50, 200, and 1000 mg/kg-bw/day (Study # 438-040, November 4, 1982; Chlorinated Paraffin Consortium). A slight decrease in viable fetuses and a slight increase in postimplantation loss were reported at 1000 mg/kg-bw/day. No other effects were reported. 
   
Based on the results of the range-finding studies, four groups of 16 Dutch Belted pregnant rabbits were administered LCCP (22-30 carbons, 70 wt% Cl) via gavage at doses of 0, 100, 300, and 1000 mg/kg-bw/day on GD 6-27 (Study # 438-039, July 18, 1983; Chlorinated Paraffin Consortium). Unmated males and females were individually housed and acclimated for 40-days in an environmentally controlled room. At the end of the acclimation period, all animals were weighed and subjected to a detailed examination. Females were impregnated via artificial insemination. Immediately after insemination, ovulation was induced via an injection of chorionic gonadotropin in a marginal ear vein. Semen was collected from males of proven fertility and evaluated for motility. The day of artificial insemination was designated as day 0 of gestation. During treatment, pregnant females were observed for mortality and clinical signs of toxicity. Body weights were recorded on GD 0, 6, 12, 18, 24, and 28. Any females not surviving to scheduled sacrifice were necropsied. On GD 28, all surviving females were sacrificed and the uterus and ovaries excised for examination. The location and number of viable and nonviable fetuses, early and late resorptions, and the number of total implantations and corpora lutea were recorded. The uterus was weighed. The thoracic and abdominal cavities underwent gross examination. Pooled samples of abdominal adipose tissue from 3 dams were frozen for future analysis. Each fetus was sexed, weighed, and examined for external malformations and variations, including the palate and the eyes, as well as visceral and skeletal examinations for malformations and developmental variations, including examination of the brain and the heart.
      
No treatment-related adverse effects were observed in the dams or the offspring at any dose level. The increases in postimplantation losses noted in the two previous range-finding studies reported above were not reproduced in the definitive study. Therefore, the NOAEL for both maternal and developmental toxicity was 1000 mg/kg-bw/day, the highest dose tested. 

 ENVIRONMENTAL MONITORING 
    MCCP MONITORING DATA 
 Surface Water
It is known that over time, based on their molecular weight and physicochemical properties, MCCPs in surface water will partition to suspended particulates, sediment, sludge, or soil. Reported MCCP concentrations in surface water range from < 2.50 x 10-10 to 1.49 x 10[-3] mg/L (Table_Apx D-1-1). Very little information is available on the specific sampling locations for many of the surface water measurements reported in Table_Apx D-1-1. Limited documentation is available on two of the studies (Petersen et al., 2006 and Muir, 2003). Two sources provide a review of the literature with very little details (IPCS, 1996 and EC, 2008b). Two studies do provide detailed information on the sampling approach, including location (Houde et al., 2008 and USEPA, 1988). The Petersen et al. (2006) study, which had the highest published concentration, reported results for water samples collected from different Norwegian locations. EPA/OPPT assumes that these samples were collected in non-marine waters. Three studies found were not used in this assessment (BUA, 1992; Hoechst, 1987; and Willis, 1994). However, all of the studies used in the assessment use modern analytical techniques, reference the specific CPs of interest, and provide, at a minimum, general information on the sampling location. Given the paucity of surface water data available, EPA/OPPT used measurements from the selected studies and used the minimum and maximum values in this assessment.

Measurements of dissolved (filtered) concentrations were generally non-detectable (ND) with few exceptions. Concentrations measured in surface water were largely from studies that measured total water concentrations which included MCCPs sorbed to particulates. More recent monitoring studies (Table_Apx D-1-1) have focused on measuring MCCPs in suspended solids, sediment pore water, and sediment. 

Early analytical methods using thin layer chromatography (TLC) were used to measure CPs in surface water. However, this method has poor sensitivity and reproducibility, and provide false negative results. Current methods of quantification using gas or liquid chromatography coupled with a range of detectors (i.e., mass spectrometry; MS) are more reliable. Nearly all of the water concentrations were measurements taken at a single point in time (i.e., the samples were not time series samples). Absent more extensive monitoring data, EPA/OPPT assumed that the available data could be extrapolated to longer time periods for determination of a chronic exposure concentration. 

MCCP concentrations in surface water, reported in Table_Apx D-1-1, rely on test methods that filtered or pre-filtered samples before they were analyzed, which can underestimate environmental concentrations. Where appropriate, reported values were converted to a common unit, as presented in the table. For the purposes of this assessment, in the studies considered acceptable, EPA/OPPT used the lowest and highest reported concentrations (< 2.50 x 10-10 to 1.49 x 10-3 mg/L; Table_Apx D-1-1) to evaluate risks of potential concern to aquatic organisms. 
Table_Apx D-1-1: Surface Water Concentrations of MCCPs, Sorted by Country
                                     Media
                                    Country
                                   Location
                            City, State or Province
                                   Comments
                            Converted Concentration
                                 Common Units
                               Analytical Method
                                  References
                                 Surface Water
                                    Canada
                                 Lake Ontario
                                    Maximum
                                 2.60x10[-9]
                                     mg/L
                                      NR
                                  EC (2008b)
                                       
                                       
                                       
                                     <
                                 2.50x10[-10]
                                     mg/L
                                  GC-HRMS-MAB
                              Houde et al. (2008)
                                       
                                       
                                       
                                     <
                                 1.00x10[-8]
                                     mg/L
                                  GC-ECNI-MS
                              Muir et al. (2003)
                                       
                                       
                                       
                                    Maximum
                                 4.70x10[-8]
                                     mg/L
                                  GC-HRMS-MAB
                              Houde et al. (2008)
                                       
                                       
                                       
                                     Mean
                                 9.00x10[-10]
                                     mg/L
                                  GC-HRMS-MAB
                              Houde et al. (2008)
                                       
                                    Germany
                            River Lech at Langsweid
                                      ---
                                 1.90x10[-4]
                                     mg/L
                                      NR
                                  IPCS (1996)
                                       
                                       
                              River Lech at Rain
                                      ---
                                 1.70x10[-4]
                                     mg/L
                                      NR
                                  IPCS (1996)
                                       
                                       
                           River Lech at Gersthofen
                                      ---
                                 9.00x10[-5]
                                     mg/L
                                      NR
                                  IPCS (1996)
                                       
                                       
                            River Lech at Augsburg
                                     <
                                 2.50x10[-5]
                                     mg/L
                                      NR
                                  IPCS (1996)
                                       
                                       
                           River Danube at Marxheim
                                      ---
                                 7.00x10[-5]
                                     mg/L
                                      NR
                                  IPCS (1996)
                                       
                                       
                                       
                                     <
                                 3.00x10[-5]
                                     mg/L
                                      NR
                                  IPCS (1996)
                                       
                                    Norway
                                      NR
                                      ---
                                 1.49x10[-3]
                                     mg/L
                                  GC-ECNI-MS
                            Petersen et al. (2006)
                                       
                                United Kingdom
                              Multiple locations
                                     <
                                   1x10[-4]
                                     mg/L
                                  GC-ECNI-MS
                            Nicholls et al. (2001)
                                       
                                 United States
                               Sugar Creek, Ohio
                                     <
                                 7.50x10[-5]
                                     mg/L
                                  GC-ECNI-MS
                                 USEPA (1988)
                                       
                           Central European Country
                                      NR
                                     <
                                 5.00x10[-5]
                                     mg/L
                                  GC-ECNI-MS
                                Coelhan (2010)
NR: Not recorded. Location description was not provided in the study.
--: Single sample value reported above the detection limit; therefore, no data qualifier required.
GC-HRMS-MAB: Gas chromatography-high resolution mass spectrometry with metastable atom bombardment ionization
GC-ECNI-MS: Gas chromatography in combination with electron capture negative ion mass spectrometry
Notes:
1. All values provided in the table above represent total MCCP and not individual MCCP isomers
2. In some cases, the minimum values in the table are preceded by "<". This indicates that the value reported in article was reported as a non-detect. In such cases, one half of the lowest reported detection limit was compiled as the `minimum' reported monitoring data
3. All concentrations measured from impoundment lagoons and drainage ditches from the USEPA (1988) study have not been included as they are not considered as surface water concentrations
4. All concentrations measured from suspended solid matter fraction from influents from the Coelhan (2010) study have not been included as they are not considered as surface water concentrations
 Sediment
MCCP sediment concentrations from marine and non-marine environments ranged from 5.00 x 10[-3] to 1.64 x 10[1] mg/kg dw and from 2.0 x 10[-3] to 6.51 x 10[1] mg/kg dw, respectively. 

For the purposes of this assessment, in the studies considered acceptable, EPA/OPPT used the lowest and highest reported marine and non-marine sediment concentrations (5.00x10[-3] to 1.64 x 10[1] mg/kg dw and 2.00 x 10[-3] to 6.51 x 10[1] mg/kg dw, respectively) to evaluate risks of potential concern to sediment organisms (Table_Apx D-1-2). Where appropriate, reported values were converted to a common unit, as presented in the table. 
Table_Apx D-1-2: Sediment Concentrations of MCCPs, Sorted by Country
                                     Media
                                    Country
                                   Location
                                   Comments
                            Converted Concentration
                                 Common Units
                                  References
                                       
                                       
                            City, State or Province
                                       
                                       
                                       
                                       
                                   Sediment
                                   (Marine)
                                   Australia
                                      NR
                                      ---
                                     1.11
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                       
                                       
                                      ---
                                     1.17
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                       
                                       
                                      ---
                                     3.11
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                       
                                       
                                      ---
                                  1.64x10[1]
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                    Canada
                      Hamilton Harbour (Windemere basin)
                                      ---
                                 2.90x10[-1]
                                    mg/kg*
                              Muir et al. (2000)
                                       
                                       
                                       
                                       
                                       
                                       
                                       
                                       
                                    Germany
                            German Bight, North Sea
                                      ---
                                 5.00x10[-3]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 9.00x10[-3]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 9.00x10[-3]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 1.30x10[-2]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 2.80x10[-2]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 1.46x10[-1]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                  Baltic Sea
                                      ---
                                 9.30x10[-2]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 1.15x10[-1]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 1.22x10[-1]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 2.11x10[-1]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                                       
                                      ---
                                 4.99x10[-1]
                                   mg/kg dw
                             Hüttig et al. (2004)
                                       
                                       
                             North and Baltic Sea
                                      ---
                                 2.20x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 2.30x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 3.30x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 3.40x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 3.70x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 3.90x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 4.30x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 4.30x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 4.80x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 5.40x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 5.80x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 6.10x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 7.20x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 7.60x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 7.70x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 8.10x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 8.50x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 8.70x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 1.49x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 1.49x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 1.49x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 2.75x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2006)
                                       
                                       
                                       
                                      ---
                                 9.10x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 4.80x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.98x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.31x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.32x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 3.03x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.53x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.14x10[-1]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 4.00x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 2.70x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.80x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.90x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 3.00x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 3.20x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 1.80x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                       
                                       
                                       
                                      ---
                                 2.40x10[-2]
                                   mg/kg dw
                           Hüttig and Oehme (2005)
                                   Sediment
                                 (Non-marine)
                                    Canada
                                   Lake Erie
                                      ---
                                 6.80x10[-2]
                                   mg/kg dw
                             Tomy and Stern (1999)
                                       
                                       
                                Lake St Francis
                                    Minimum
                                 7.50x10[-1]
                                   mg/kg dw
                                  EC (2008b)
                                       
                                       
                                       
                                    Maximum
                                      1.2
                                   mg/kg dw
                                  EC (2008b)
                                       
                                Czech Republic
                                      NR
                                    Minimum
                                 2.00x10[-3]
                                    mg/kg*
                            Pribylova et al. (2006)
                                       
                                       
                                     Labe
                                      Sum
                                 1.80x10[-2]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                       
                                      Sum
                                 7.30x10[-2]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                  Libis-Labe
                                      Sum
                                      1.6
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                    Bilina
                                      Sum
                                 3.10x10[-2]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                  Mala Becva
                                      Sum
                                 1.13x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                     Becva
                                      Sum
                                 1.20x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                    Morava
                                      Sum
                                 1.93x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                     Ohre
                                      Sum
                                 3.08x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                       
                                      Sum
                                 6.00x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                       
                                      Sum
                                     5.58
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                    Morava
                                      Sum
                                 4.16x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                     Dyje
                                      Sum
                                 7.57x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                       
                                   Drevnice
                                      Sum
                                 8.93x10[-1]
                                   mg/kg dw
                            Pribylova et al. (2006)
                                       
                                    Germany
                               Bodensee (middle)
                                     <
                                 5.00x10[-3]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                      ---
                                 7.00x10[-2]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                  River Lech
                                     <
                                 5.00x10[-3]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                      ---
                                 3.25x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                    Maximum
                                 7.00x10[-1]
                                    mg/kg*
                              Tomy et al. (1998)
                                       
                                       
                                  River Rhine
                                      ---
                                 6.00x10[-2]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                      ---
                                 8.50x10[-2]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                      ---
                                 1.40x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                    Minimum
                                 1.45x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                    Maximum
                                 2.05x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                             River Elbe at Hamburg
                                    Minimum
                                 1.30x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                    Maximum
                                 2.30x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                  River Main
                                    Minimum
                                 1.60x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                                       
                                    Maximum
                                 2.60x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                       
                             Outer Alster, Hamburg
                                      ---
                                 3.70x10[-1]
                                   mg/kg dw
                                  IPCS (1996)
                                       
                                    Norway
                                      NR
                                    minimum
                                 5.00x10[-2]
                                   mg/kg dw
                            Petersen et al. (2006)
                                       
                                       
                                       
                                    maximum
                                     3.24
                                   mg/kg dw
                            Petersen et al. (2006)
                                       
                                       
                                       
                                      ---
                                      2.7
                                   mg/kg ww
                             Borgen et al. (2003)
                                       
                                       
                                       
                                      ---
                                  1.14x10[1]
                                   mg/kg ww
                             Borgen et al. (2003)
                                       
                                  South China
                               Pearl River Delta
                                    Minimum
                                 8.80x10[-1]
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                    Minimum
                                      1.1
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                    Minimum
                                      1.4
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                    Maximum
                                      1.4
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                    Maximum
                                      3.8
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                     Mean
                                      3.9
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                     Mean
                                  2.10x10[1]
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                       
                                       
                                    Maximum
                                  3.80x10[1]
                                   mg/kg dw
                              Chen et al. (2011)
                                       
                                  Switzerland
                                   Lake Thun
                                    Minimum
                                 5.00x10[-3]
                                   mg/kg dw
                              Iozza et al. (2008)
                                       
                                       
                                       
                                    Maximum
                                 2.60x10[-2]
                                   mg/kg dw
                              Iozza et al. (2008)
                                       
                                       
                                  Lake Zurich
                                    Maximum
                                 5.00x10[-3]
                                    mg/kg*
                              Tomy et al. (1998)
                                       
                                United Kingdom
                                      NR
                                     <
                                 1.00x10[-1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                     South West Region: Grand Union Canal
                                      ---
                                 3.00x10[-1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                      2.7
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                      2.8
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                     South West Region; Bristol Avon River
                                      ---
                                 5.00x10[-1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                 6.00x10[-1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                 8.00x10[-1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                         North East Region: Hull River
                                      ---
                                      1.0
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  1.35x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                      1.1
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                        South West Region: Colne River
                                      ---
                                      1.4
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                      2.0
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                       West Midlands Region: Trent River
                                      ---
                                      3.8
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  6.02x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  6.51x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                      North West Region: Hornsmill brook
                                      ---
                                      5.6
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  1.25x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  1.83x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                         North East Region: Hull River
                                      ---
                                      1.0
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                      1.1
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  1.35x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                       East Midlands Region: Idle River
                                      ---
                                  1.62x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  4.39x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                      Northumberland Region: Skerne River
                                      ---
                                  1.80x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  2.56x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  5.84x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                        East Anglia Region: Lark River
                                      ---
                                  3.22x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  4.50x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                       
                                       
                                      ---
                                  6.04x10[1]
                                   mg/kg dw
                            Nicholls et al. (2001)
                                       
                                 United States
                                 Detroit River
                                      ---
                                 6.80x10[-2]
                                   mg/kg dw
                              Tomy et al. (1999)
                                       
                                       
                               Sugar Creek, Ohio
            Reported as trace with range of 1.5-5; used the average
                                 3.25x10[-3]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
            Reported as trace with range of 1.5-5; used the average
                                 3.25x10[-3]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
                                      ---
                                 6.80x10[-3]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
                                      ---
                                 8.20x10[-3]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
                                      ---
                                 7.60x10[-1]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
                                      ---
                                  2.10x10[1]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
                                      ---
                                  3.40x10[1]
                                   mg/kg dw
                                 USEPA (1988)
                                       
                                       
                                       
                                      ---
                                  5.00x10[1]
                                   mg/kg dw
                                 USEPA (1988)
Note:
NR: Not recorded. Location description was not provided in the study.
--: Single sample value reported above the detection limit; therefore, no data qualifier required.
1. All values provided in the table above represent total MCCP and not individual MCCP isomers
2. In some cases, the minimum values in the table are preceded by "<". This indicates that the value reported in article was reported as a non-detect. In such cases, one half of the lowest reported detection limit was compiled as the `minimum' reported monitoring data 
3. dw   -   dry weight and ww   -   wet weight

 Biosolids and Soil
CPs are detected more frequently and at higher concentrations in treated sewage sludge (i.e., biosolids) than in soil. MCCP concentrations ranged from 5.00 x 10[-5] to 9.70 x 10[3] mg/kg dw in sludge and from 1.5 x 10[-2] to 8.5 x 10[-2] mg/kg dw in soil. It is unclear if the difference in MCCP concentrations in sludge and soil is related to the smaller sample sizes for these media compared to the typically larger data sets available for water and sediment. To determine the most reliable studies for its consideration, EPA/OPPT used the following criteria: designation of specific MCCP chain length and the appropriate analytical methodology. Based these criteria, EPA/OPPT determined that the data reported by Stevens et al. (2003) were the most reliable for its use in this assessment: data are summarized below. 

Stevens et al. (2003) measured MCCP concentrations in sludge samples obtained from 14 WWTPs in the UK. MCCP concentrations ranged from 3.00 x 10[1] to 9.70 x 10[3] mg/kg dw. The authors concluded that these very high concentrations were likely the result of releases from numerous and ongoing diffuse sources. EPA/OPPT did not use information from other published studies reporting measured CPs in sludge and soil because they did not distinguish the CPs measured  (Nicholls et al., 2001). These studies reported total CP concentrations at much lower levels ranging from 3.00 x 10[-5] to 2.3 mg/kg dw. 

Although risk to terrestrial species was not calculated, EPA/OPPT notes that the lowest and highest reported biosolid and soil concentrations (5.00 x 10[-5] to 9.70 x 10[3] mg/kg dw and 1.5 x 10[-2] to 8.5 x 10[-2] mg/kg dw, respectively) represents a very large range (up to eight orders of magnitude (Table_Apx D-1-3). 

Table_Apx D-1-3: Biosolid and Soil Concentrations of MCCPs 
Location
                                     Media
                                 Concentration
                                     Units
                                  References

                                       
                                    Minimum
                                    Maximum
                                       
                                       
Switzerland
                                     Soil
                                1.5 x 10[-2] 
                                 8.5 x 10[-2]
                                   mg/kg dw
                                 Iozza (2010)
China
                                     Soil
                                 2.1 x 10[-6]
                                1.53 x 10[-3]
                                   mg/kg dw
                              Wang et al. (2013)
Czech Republic
                                 Sewage Sludge
                                7.36 x 10[-1]
                                     2.30
                                   mg/kg dw
                            Pribylova et al. (2006)
United Kingdom
                                 Sewage Sludge
                                 3.00 x 10[1]
                                 9.70 x 10[3]
                                   mg/kg dw
                             Stevens et al. (2003)
United States
                                 Sewage Sludge
                                5.00 x 10[-5]
                                5.00 x 10[-5]
                                   mg/kg dw
                            Pribylova et al. (2006)

 Biota
EPA/OPPT reviewed available published literature and summarized MCCP concentrations in tissues of aquatic and terrestrial biota (Table_Apx D-1-4). Measured tissue concentrations for aquatic biota ranged from ND to 2.63 mg/kg ww (i.e., beluga whales, seals, rainbow trout, carp, mackerel, arctic char, mussels, crustaceans, and plankton) and ranged from 5.00 x 10[-3] to 3.70 x 10[-1] mg/kg ww in terrestrial biota. The concentrations measured in the terrestrial studies did not designate the specific CP congeners measured. 
As a result of EPA/OPPT's evaluation, MCCPs were found in organisms across many different trophic levels indicating widespread environmental contamination (Table_Apx D-1-4). The data were insufficient for EPA/OPPT to draw conclusions about trends based on region, species, time, or other factors.

While EPA/OPPT determined the concentrations of MCCPs in aquatic and terrestrial biota range from ND to 2.63 mg/kg ww from 5.00 x 10[-3] to 3.70 x 10[-1] mg/kg ww, respectively, in this assessment, EPA/OPPT did not use tissue concentrations to determine risks of potential concern for biota Table_Apx D-1-4. Rather, it used the risk quotient (RQ) method as described in Section 6.

Table_Apx D-1-4: Biota Concentrations of MCCPs
 Location
                               Media Description
                                    Minimum
                                     Units
                                 Min Reference
                                    Maximum
                                     Units
                                 Max Reference
 
                                        
                                        
                                        
                                        
                                        
                                        
                                        
                                 Aquatic Biota
 Australia
                                 Invertebrates
                                  2.32x10[-5]
                                    mg/kg lw
                             Kemmlein et al. (2002)
                                  3.05x10[-5]
                                    mg/kg lw
                             Kemmlein et al. (2002)
 Canada
                                    Mammals
                                  5.45x10[-7]
                                    mg/kg ww
                              Bennie et al. (2000)
                                  8.00x10[-5]
                                    mg/kg ww
                              Bennie et al. (2000)
 
                                      Fish
                                  2.57x10[-7]
                                    mg/kg ww
                              Bennie et al. (2000)
                                      2.63
                                    mg/kg ww
                               Muir et al. (2000)
 
                                 Invertebrates
                                     ND[1]
                                    mg/kg ww
                                   EC (1993)
                                     ND[1]
                                    mg/kg ww
                                   EC (1993)
 
                                     Total
                                     ND[1]
                                    mg/kg ww
                                   EC (1993)
                                      2.63
                                    mg/kg ww
                               Muir et al. (2000)
 Europe
                                      Fish
                                  7.00x10[-3]
                                    mg/kg ww
                               Reth et al. (2006)
                                  4.70x10[-2]
                                    mg/kg ww
                               Reth et al. (2006)
 North Sea/Baltic Sea Region[2]
                                      Fish
                                     ND[3]
                                    mg/kg ww
                                   IVL (2009)
                                  2.6x10[-1]
                                    mg/kg ww
                               Reth et al. (2005)
 United States
                                      Fish
                                  2.90x10[-3]
                                    mg/kg ww
                             Tomy and Stern (1999)
                                  9.04x10[-1]
                                    mg/kg ww
                             Tomy and Stern (1999)
 
                                 Invertebrates
                                  3.50x10[-3]
                                    mg/kg ww
                                  USEPA (1988)
                                  1.70x10[-1]
                                    mg/kg ww
                                  USEPA (1988)
 
                                     Total
                                  2.90x10[-3]
                                    mg/kg ww
                             Tomy and Stern (1999)
                                  9.04x10[-1]
                                    mg/kg ww
                             Tomy and Stern (1999)
 United States / Canada 
- Great Lakes 
                                      Fish
                                  1.80x10[-3]
                                    mg/kg ww
                               Muir et al. (2003)
                                  1.10x10[-1]
                                    mg/kg ww
                               Muir et al. (2003)
 
                                 Invertebrates
                                  2.40x10[-3]
                                    mg/kg ww
                                   EC (2008a)
                                  1.60x10[-2]
                                    mg/kg ww
                               Muir et al. (2003)
 
                                     Total
                                  1.80x10[-3]
                                    mg/kg ww
                               Muir et al. (2003)
                                  1.10x10[-1]
                                   mg/kg ww.
                               Muir et al. (2003)
                               Terrestrial Biota
 Europe
                                     Birds
                                  5.00x10[-3]
                                    mg/kg ww
                               Reth et al. (2006)
                                  3.70x10[-1]
                                    mg/kg ww
                               Reth et al. (2006)
 Notes:
 Summary values represent total MCCP and not individual MCCP isomers.
 [1] MCCPs were not detected in Invertebrates from Canada. Detection limit = 4.0 x 10[-7] mg/kg; (1/2) DL = 2.0 x 10[-7] (EC, 1993).
 [2] North Sea/Baltic Sea Region includes the following countries: Estonia, Latvia, Lithuania, Norway, Poland, and Sweden.
 [3] The minimum MCCP concentration value for fish from the North Sea/Baltic Sea Region was non-detect. The detection limit = 2.5 x 10[-4] mg/kg; (1/2) DL = 1.25 x 10[-4] (IVL 2009)

    LCCP MONITORING DATA 
Kemmlein et al. (2002) optimized and tested the carbon skeleton reaction gas chromatography analytical method to analyze environmental samples for CPs. The optimized method was used for marine sediments, mussels and crabs taken from an area influenced by a CP manufacturer in Yarraville, Australia. LCCP (C18-20) concentrations in marine sediment ranged from 1.02 x 10[-1] to 4.31 x 10[-1] mg/kg dw (Table_Apx D-2-1), those in mussels ranged from 4 x 10[-1] to 1.9 mg/kg lw, and those in crab ranged from 3 x 10[-2] to 4.4 mg/kg lw. The results presented in this paper show that bioaccumulation is evident. The mussel samples contained approximately two times and crab tissue around six times the concentration of CPs found in the most contaminated sediment sample. No other adequate studies were found to characterize LCCP concentrations in surface water, fresh water sediment or soil.

Table_Apx D-2-1: Marine Sediment Concentrations of LCCPs
                                     Media
                                    Country
                                   Location
                                   Comments
                                 Concentration
                                     Units
                                  References
                                       
                                       
                            City, State or Province
                                       
                                       
                                       
                                       
                                   Sediment
                                   (Marine)
                                   Australia
                                      NR
                                      Sum
                                 1.02x10[-1]
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                       
                                       
                                      Sum
                                 1.28x10[-1]
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                       
                                       
                                      Sum
                                 3.04x10[-1]
                                   mg/kg dw
                            Kemmlein et al. (2002)
                                       
                                       
                                       
                                      Sum
                                 4.31x10[-1]
                                   mg/kg dw
                            Kemmlein et al. (2002)
Notes:
    Values provided in the table above represent total LCCP (C18-20) and not individual isomers.
    dw  -  dry weight

Table_Apx D-2-2: Biota Concentrations of LCCPs
                                     Media
                                    Country
                                   Location
                                    Minimum
                                    Maximum
                                     Units
                                  References
                                       
                                       
                            City, State or Province
                                       
                                       
                                       
                                       
                                 Aquatic Biota
                                   Australia
                                      NR
                                 2.89x10[-6]
                                 6.90x10[-6]
                                   mg/kg lw
                            Kemmlein et al. (2002)
Notes:
    Minimum and Maximum concentrations provided in the table above represent total LCCP (C18-20) and not individual isomers.
    lw  -  lipid weight
                                       

 ENGINEERING (ChemSTEER) REPORTS ON P-12-0-0433 and P-12-0453 
 (Used for both identifying potential releases to the environment and for estimated occupational exposures. SEE APPENDIX G FOR REFERENCE TO FULL REPORTS UNDER SEPARATE COVER)

INITIAL REVIEW ENGINERING REPORT

P-12-0433
Post Focus Review Draft 10/13/2016

This section provides details on EPA's original engineering assessment of occupational exposure and environmental releases from 2012 as well as the Expanded EPA assessment from 2016.  

ENGINEER: Macek
PV (kg/yr): 23,138 Import Only 

Revision Notes/Assessment Overview: 06/29/16 Update: This IRER was revised to utilize the methodologies from 2 CP assessments in 2015. Industry comments were also used in this assessment. Changes include: providing several release scenarios for all uses (using WWT removal efficiencies of 50, 70 and 99% as well as assuming monthly and quarterly release of container residuals per industry practices). Occupational assessments remained the same as in the previous version of this IRER. However, dermal assessments increases as a result of a larger hand surface area used as default in dermal exposure calculations. 

SUBMITTER: INEOS Chlor Americas 

USE: 100% of the notification substance is used as a lubricant in metal working fluids (MWFs). The notification substance is blended into the MWFs.
OTHER USES: Generic uses MCCP: 1) Forty-three percent of the notification substances are used as a flame retardant/plasticizer in polymers. Typical concentration in the plastic is 12-30%. 2) Thirty percent of the notification substance is used as a lubricant in metal working fluids (MWFs). The notification substance is blended into the MWFs at 5-10%. 3) Two percent of the notification substances is used as lubricants in automotive. The notification substances is blended into the lubricant at 4%. [20% consumer uses]. 4) Twenty-four percent of the notification substance is used as a flame retardant/plasticizer in rubber. Typical total concentration of flame retardant/plasticizer in the rubber is 1-10%, with a media value of 5.5%. 5) One-half of one percent of the notification substances are used as plasticizer in solvent based paints, adhesives and sealants. The paints are specialty paints for applications where weather resistant coatings are needed, such as steel construction, industrial flooring, road marking, and swimming pools. The notification substance is blended into the paints at 5-15%. [0.1% consumer uses as sealants in windows] and 6) One-half of one percent of the notification substances are applied as a flame retardant/waterproofers to textiles. The notification substance products are added at 5% of the textile coating finishing solution. 

MSDS:  Yes										LABEL: No

Gen Eqpt: If prolonged or excessive skin contact is likely: Wear suitable protective clothing and gloves. // If splashing or mist is likely to occur: Wear eye/face protection.
Respirator: No information provided in MSDS.
Health Effects: Eye: may cause slight eye irritation. // Skin: unlikely to cause skin irritation in man. // Ingestion: unlikely to be hazardous if swallowed. // Inhalation: unlikely to be hazardous by inhalation. // Chronic Effects: repeated exposure to high levels may product liver and kidney damage.
TLV/PEL: - none established

CRSS:
Chemical Name: Alkanes, C18‑20, chloro
S-H2O: 0.000006 g/L @
VP: 4.0E-6 torr @
MW: 412 %<500 %<1000
Physical State and Misc CRSS Info: Neat: liquid	Mfg: liquid
Proc/Form: liquid	End Use: 15% in final product. The chlorinated products would range from C17H31Cl5 (at ~40% chlorination) to C20H34Cl8 (at ~50% chlorination).  The parent hydrocarbon had a measured composition: C17: 17.06% (max 20) C18: 64.71% (45‑70) C19: 13.67% (15‑27) C20: 2.13% (4‑12) The chlorination content looks to range between roughly 40 ‑ 55%.

Consumer Use: No

SAT (concerns):
SAT data not yet available
Related Cases and Misc SAT Info:
SAT data not yet available
Migration to groundwater: 
PBT rating: PBT SAT data not yet available
Health: 
Eco: 

OCCUPATIONAL EXPOSURE RATING: 2D

NOTES & KEY ASSUMPTIONS:
06/29/16 Update: This IRER was revised to utilize the methodologies from 2 CP assessments completed in 2015. Industry comments were also used in this assessment. Changes include: providing several release scenarios for all uses (using WWT removal efficiencies of 50, 70 and 99% as well as assuming monthly and quarterly release of container residuals per industry practices). Occupational assessments remained the same as in the previous version of this IRER. However, dermal assessments increase as a result of a larger hand surface area used as default in dermal exposure calculations.  The remaining portion of this provides information from the previous assessment. Generated by the 09/30/2013 version of ChemSTEER. ***   Generated by the 06/07/2005 version of ChemSTEER. This PMN is a liquid LCCP product that is imported and used as a lubricant in metal working fluids // Note, the SAT information is not yet available for this PMN. // Note, one of four exposure based criteria were met. // For PROC: This IRER assesses releases based on information provided in EU RAs and a CSR provided by the submitter and EPA/OPPT standard models. Dermal exposures were assessed and inhalation exposure is expected to negl. (VP < 0.001 torr). // For USE: This IRER assesses releases based on the 2011 ESD for the Use of Metalworking Fluids and EU RAs provided by the submitter. Dermal and inhalation exposures were assessed per the ESD. // No same‑submitter, same‑use past cases were identified. This IRER uses the same release and exposure assessment methodology as presented in different‑submitter, same‑use past cases P12‑0277 through P12‑0282. The submitter of this IRER provided the same references that were used in the assessment of MWF formulation and use for these past cases and, therefore, this IRER performs an assessment a similar manner.

POLLUTION PREVENTION CONSIDERATIONS:

EXPOSURE-BASED REVIEW: Yes	(1 criteria met)

 # of workers exposed: 216 >1000? No
 >100 workers with >10 mg/day inhalation exposure: No
 (a) >100 workers w/1-10 mg/day inh. exp. & >100 days/yr: Yes
 (b) Routine Dermal Cont: >250 workers & >100 days/yr: Yes

PROC1: Formulation of Metalworking Fluids
Number of Sites/Location: 3 sites
Unknown site(s)

Basis: The submission does not provide information on the number of customers and or use rate of the PMN in MWF formulation. The submission states that the PMN is formulated in MWFs at a conc of 10-20% for neat oils and 5% for emulsions with a typical conc of 15%. Based on different-submitter, same-use past case P12-0277 for a similar PMN substance (liquid LCCP), 69 formulation sites were estimated for a production volume of 616,763 kg/yr. Using this as a basis, CEB estimates the number of formulation sites for a PV of 23,138 kg/yr as (23,138/619 763) * 69 ~ 3 sites. Batch size at formulation sites is unknown.  Previous larger-scale related PMN submissions (P-12-0277 and P-12-0357) estimated batch sizes at MW Fluid formulation sites of greater than 1000 gallons.  CEB assumes a batch size of at least 500 gallons (equivalent to 283 kg of PMN chemical at 15% concentration) to estimate the kg/batch and number of batches.

Process Description: PMN (liquid, 100%) is unloaded from import containers ---> feed into blending tank ---> packaging of metal working fluids containing PMN (10-20% for neat oil and 5% for emulsions) (submission past Std Review cases for CPs)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The release estimates were based on a combination of data from documents provided by the submitter as well as EPA/OPPT standard models.

2012 EPA Assessment
Water or Incineration or Landfill
High End: 8.6E+0 kg/site-day over 27 day/yr from 3 sites 
to: uncertain
2016 Expanded EPA Assessment (Oil-based fluids)
Water or Incineration or Landfill
Monthly: 1.4E+1 kg/site-day over 12 day/yr from 2 sites 
Quarterly: 4.3E+1 kg/site-day over 4 day/yr from 2 sites
to: Uncertain
2016 EPA Expanded Assessment (water based, on-site pretreatment with 50% efficiency)
Water or Incineration or Landfill
Monthly: 7.2E+0 kg/site-day over 12 day/yr from 2 sites 
Quarterly: 2.2E+1 kg/site-day over 4 day/yr from 2 sites
to: Pretreatment (50% removal efficiency) then to POTW, incineration or landfill
2016 EPA Expanded Assessment (water based, on-site pretreatment with 70% efficiency)
Water or Incineration or Landfill
Monthly: 4.3E+0 kg/site-day over 12 day/yr from 2 sites 
Quarterly: 1.3E+1 kg/site-day over 4 day/yr from 2 sites
to: Pretreatment (70% removal efficiency) then to POTW, incineration or landfill
2016 EPA Expanded Assessment (water based, on-site pretreatment with 99% efficiency)
Water or Incineration or Landfill
Monthly: 1.4E-1 kg/site-day over 12 day/yr from 2 sites 
Quarterly: 4.3E-1 kg/site-day over 4 day/yr from 2 sites
to: Pretreatment (99% removal efficiency) then to POTW, incineration or landfill
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: EPA/OPPT Drum Residual Model, CEB standard 3% residual. The submission does not provide information to estimate releases from container cleaning. Due to uncertainty at multiple downstream sites, CEB assesses releases to uncertain media using the standard model loss fraction of 3%.
2016 EPA Expanded Assessment (Oil-Based Fluids):Assumes quarterly or monthly container cleaning, per industry information indicating containers are not picked up daily by a waste handler. 
2016 EPA Expanded Assessment (water based, on-site pretreatment with 50%, 70% and 99% efficiency): Assumes quarterly or monthly container cleaning, per industry information indicating containers are not picked up daily by a waste handler. Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water or Incineration or Landfill
Conservative: 5.7E+0 kg/site-day over 27 day/yr from 3 sites
to: Uncertain
2016 Expanded EPA Assessment (Oil-based fluids)
Incineration or Landfill
Conservative: 2.8E+0 kg/site-day over 20 day/yr from 2 sites 
to: Incineration or Landfill (industry comments)
2016 Expanded EPA Assessment (water-based, on-site pretreatment with 50% efficiency)
Water or Incineration or Landfill
Conservative: 4.8E-1 kg/site-day over 61 day/yr from 2 sites or 
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (water-based, on-site pretreatment with 70% efficiency)
Water or Incineration or Landfill
Conservative: 2.8E-1 kg/site-day over 61 day/yr from 2 sites 
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (water-based, on-site pretreatment with 99% efficiency)
Water or Incineration or Landfill
Conservative: 9.5E-3 kg/site-day over 61 day/yr from 2 sites 
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Equipment Cleaning Losses of Liquids from a Mixing Tank
basis: EPA/OPPT Multiple Process Vessel Residual Model, CEB standard 2% residual. The submission does not provide information to estimates releases from equipment cleaning. Due to uncertainty at multiple downstream sites, CEB assesses releases to uncertain media using the standard model loss fraction of 2%.
2016 EPA Expanded Assessment (Oil-Based Fluids):  Industry information indicates cleaning of equipment that is in contact with MCCPs would not use water. Therefore, wastes are assumed to incineration or landfill.  
2016 EPA Expanded Assessment (water based, on-site pretreatment with 50%, 70% and 99% efficiency):  Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

Air
Output 2: 5.7E-1 kg/site-day over 27 day/yr from 3 sites 
to: fugitive air (2005 EU RA, 2009 EU RA)
from: Fugitive Air Emissions
basis: User-Defined Loss Rate Model. Data from a 2005 EU RA for MCCP provided by the submitter estimates 16 kg/yr of MCCP may be released to air from fugitive air emissions generated by preheating and blending at a typical MWF formulation site (16 kg/yr / 7,713 kg/site-yr =  0.2% for the current operations). A 2009 EU RA for LCCPs provided by the submitter estimates a loss of 58 g/day, or 14.5 kg/yr assuming 250 days/yr of operation (14.5/7,713  = 0.19% for current operations). Due to uncertainty at multiple downstream use sites, CEB includes this release source using the high end estimate.

Incineration or Landfill
Output 2: 5.7E+0 kg/site-day over 27 day/yr from 3 sites 
to: incineration or landfill (2009 EU RA)
from: Off-Spec Material
basis: User-Defined Loss Rate Model. Data from a 2009 EU RA for LCCPs estimates a 1-2% loss rate from disposal of off-spec batches released to solid waste. Due to uncertainty at multiple downstream use sites, CEB includes this release source using the high end estimate with releases to incineration or landfill.

RELEASE TOTAL

2012 EPA Assessment: 1.7E+3 kg/yr - all sites
2016 EPA Expanded Assessment (Oil-Based Fluids): 6.9E+2 kg/yr - all sites
2016 EPA Expanded Assessment (water-based, on-site pretreatment with 50% efficiency): 6.4E+2 kg/yr - all sites
2016 EPA Expanded Assessment (water-based, on-site pretreatment with 70% efficiency): 4.8E+2 kg/yr - all sites
2016 EPA Expanded Assessment (water-based, on-site pretreatment with 99% efficiency): 2.4E+2 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 24
Basis: The submission does not provide an estimate for the number of workers/site. Previous related submissions (p-12-0277 to P-12-0284) indicated 4 to 8 workers per site.  CEB assumes 8.

Inhalation:
Negligible due to low vapor pressure (VP < 0.001 torr) and physical state as handled (liquid).  

Dermal:

Exposure to Liquid
High End: 2.2E+3 mg/day over 27 days/yr
Number of workers (all sites) with Dermal exposure: 24
Basis: Unloading Liquid Raw Material from Totes and Tank Trucks; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

Dermal:

Exposure to Liquid
High End: 4.5E+2 mg/day over 27 days/yr
Number of workers (all sites) with Dermal exposure: 24
Basis: Loading Liquid Product into Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

USE1: Use of Metalworking Fluids 
Number of Sites/Location: 4 sites
unknown site(s)

Days/yr: 247 

Basis: he submission does not provide any information for end use of MWFs. The submission estimates a typical conc of PMN in MWFs of 15%. The 2011 ESD for MWF Operations estimates 247 days/yr of operation. The ESD
estimates the number of sites as: (23,138 kg/yr) / (12,000 gal/site-yr x 1 kg/L x 3.785 L/gal x 0.15) ~ 4 sites. Environmental releases are of concern for this PMN. As conservative, CEB assumes 247 days/yr of operation and the ESD estimate of 4 sites. CEB also assumes up to 20% PMN in raw material, and 2% PMN during metalworking operations. CS calcualtes a use rate of 23.4192 kg/site-day.
Process Description: Bulk MWF containing PMN (liquid, 10-20 percent neat oil or 5% emulsion) is unloaded from transport containers ---> transfer to mixing vessel ---> dilution of MWF ---> diluted MWF containing PMN (liquid, assume 1-2% for neat oil and 0.5% for emulsion assuming a 10 fold dilution) transferred to metal shaping trough ---> metal shaping operation ---> shaped metal part is rinsed and dried ---> spent MWF is drained and discarded (submission, ESD, past std review cases for CPs)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The releases estimates were based data provided in reports provided by the submitter as well as the 2011 ESD for the Use of Metalworking Fluids.

2012 EPA Assessment
Water or Incineration or Landfill
High End: 1.2E+0 kg/site-day over 139 day/yr from 4 sites 
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Oil-Based Fluids)
Incineration or Landfill
High End: 1.2E+0 kg/site-day over 69 day/yr from 4 sites
to: incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water, Incineration or Landfill
High End: 1.8E-1 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water, Incineration or Landfill
High End: 1.1E-1 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water, Incineration or Landfill
High End: 3.5E-3 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: EPA/OPPT Drum Residual Model, CEB standard 3% residual. The submission does not provide estimates for releases during MWF use. Due to uncertainty at multiple downstream sites, these releases are assessed to uncertain media using a 3% loss rate per the ESD..
2016 Expanded EPA Assessment (Oil-Based Fluids): 2011 OECD ESD for Use of Metalworking Fluids assesses drums residuals for oil-based fluids to incineration or landfill.
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency). Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water
Output 2: 2.5E+0 kg/site-day over 247 day/yr from 4 sites
to: on-site WWTP or POTW (ESD)
2016 Expanded EPA Assessment (Oil-Based Fluids)
Water or Incineration or Landfill
Output 2: 1.2E+0 kg/site-day over 247 day/yr from 4 sites 
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water
High End: 6.2E-1 kg/site-day over 247 day/yr from 4 sites
to: on-site WWTP or POTW (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water
High End: 3.7E-1 kg/site-day over 247 day/yr from 4 sites
to: on-site WWTP or POTW (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water
High End: 1.2E-2 kg/site-day over 247 day/yr from 4 sites
to: on-site WWTP or POTW (ESD)
from: Dragout Losses
basis: User-Defined Loss Rate Model. A 2005 EU RA for MCCPs and a 2009 EU RA for LCCPs provided by the submission estimates workpiece dragout to account for 1 to 2% with releases water or chemical waste and grinding swarf dragout is estimated to be 30 to 90% with releases to incineration or landfill. The 2011 ESD for MWF Operations estimates a loss rate of 11% from dragout with releases to on-site WWTP or POTW. These data are based on U.S. industry data collected during the development of effluent guidelines for the metalworking industry. These data provide the best representation of U.S. operations and are more conservative than the submitter estimates. Due to uncertainty at multiple downstream sites, CEB assesses dragout releases using the ESD estimate of 11% and accounting for upstream losses from container cleaning: (1-0.03) x 0.11 = 0.1067. Releases are assessed to water via on-site WWTP or POTW per submission and ESD. The data from the 2011 ESD is most representative of U.S. industry and is therefore used as the basis for releases.
2016 Expanded EPA Assessment¨ 2011 OECD ESD for Use of Metalworking Fluids assesses dragout losses of metalworking fluids for oil-based fluids to water, incineration or landfill. 
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency).  Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water or Incineration or Landfill
Output 2: 8.2E+0 kg/site-day over 247 day/yr from 4 sites
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Oil-Based Fluids)
Incineration or Landfill
Output 2: 4.1E+0 kg/site-day over 247 day/yr from 4 sites
to: incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water, Incineration or Landfill
High End: 2.0E+0 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water, Incineration or Landfill
High End: 1.2E+0 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water, Incineration or Landfill
High End: 4.1E-2 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Filter Media and Other Recycling Waste
basis: User-Defined Loss Rate Model. The 2011 ESD for MWF Operations estimates these releases to account for a 36% loss rate with releases to water, incineration, or landfill (water-based fluids) or incineration or landfill (straight-oil). Accounting for upstream container cleaning losses: (1-0.03) x 0.36 = 0.3492. CEB assesses these releases to water, incineration, or landfill based on uncertainty at multiple downstream use sites.
2016 Expanded EPA Assessment (Oil-Based Fluids) 2011 OECD ESD for Use of Metalworking Fluids assesses disposal of filter media and other recycling waste to incineration or landfill for oil-based fluids. 
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency). Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water or Incineration or Landfill
Output 2: 1.0E+1 kg/site-day over 247 day/yr from 4 sites
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment Oil-Based Fluids)
Incineration or Landfill
Output 2: 6.0E+0 kg/site-day over 247 day/yr from 4 sites
to: incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water, Incineration or Landfill
High End: 3.0E+0 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water, Incineration or Landfill
High End: 1.8E+0 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water, Incineration or Landfill
High End: 6.0E-2 kg/site-day over 247 day/yr from 4 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Spent Metalworking Fluid
basis: User-Defined Loss Rate Model.  The 2011 ESD for MWF Operations also assesses 100% release with the spent MWF disposed to water (water-based fluids) or incineration or landfill (straight oil fluids) with at least one bath changeout occurring per day at a facility with multiple baths in use. Based on uncertainty at multiple downstream use sites, CEB assesses the spent MWF to water, incineration, or landfill. Account for upstream losses, the loss rate is calculated as: (1-0.03) x (1-0.05-0.11-0.38) = 0.4462.
2016 Expanded EPA Assessment (Oil-Based Fluids) 2011 OECD ESD for Use of Metalworking Fluids assesses disposal of spent metalworking fluid to incineration or landfill for oil-based fluids.  
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency). Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Air
Output 2: 1.1E+0 kg/site-day over 247 day/yr from 4 sites 
to: air (2002 EU RA)
from: Misting/Evaporation
basis: User-Defined Loss Rate Model. A 2005 EU RA for MCCP and a 2009 EU RA for LCCPs provided by the submitter estimates misting/evaporation losses to range from 2 to 5% depending on the type of MWF begin used. Based on uncertainty at multiple downstream sites, CEB uses the most conservative estimate of 5% loss to air from misting/evaporation. Account for upstream losses from container cleaning: (1-0.03) x 0.05 = 0.0485.
EPA 2016 Expanded Assessment: This release source was removed.

RELEASE TOTAL

2012 EPA Assessment: 2.3E+4 kg/yr - all sites
2016 Expanded EPA Assessment (Oil-Based Fluids): 1.2E+4 kg/yr - all sites
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment): 5.8E+3 kg/yr - all sites
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment): 3.5E+3 kg/yr - all sites
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment): 2.3E+2 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 192
Basis: The 2011 ESD for MWF Use estimates 48 workers/site. 
Inhalation:

Exposure to Mist
High End of Range: 7.1E+0 mg/day over 247 days/yr
Typical: 2.0E+0 mg/day over 247 days/yr
Number of workers (all sites) with Inhalation exposure: 192
Basis: Exposure During Metalworking Operation; User-defined Inhalation Model. The 2011 ESD for MWF Operations estimates typical mist concentrations ranging from 0.19 to 0.39 mg/m[3] and high end concentrations ranging from 0.87 to 1.42 mg/m[3] depending on the type of MWF used. These estimates are based on the geometric mean (typical) and 90th percentile data (high end) of data collected by NIOSH from 942 machinists at 79 shops across the U.S. A range of inhalation exposure estimates are based the high end for the range of geometric means and 90th percentiles. CEB assumes water portion is 60% of fluid.  Based on up to 20% concentration of PMN chemical in the neat fluid, the concentration of the PMN chemical in the mist could be as high as 50% (20%/40%).  Note, a 2005 EU RA for MCCPs and a 2009 EU RA for LCCPs estimates mist concentrations from 1.6 to 3.4 mg/m3 based on the 95th percentile of data collected in the EU for oil-based and water-based fluids. The data from the 2011 ESD are more representative of U.S. operations since the data were collected in the U.S.

INHALATION MONITORING DATA REVIEW

 Uncertainty (estimate based on model, regulatory limit, or data not specific to industry): Yes
 (a) Exposure level >1 mg/day? Yes
   (b) Hazard Rating for health of 2 or greater? No
Inhalation Monitoring Data Desired? Yes (both criteria met)

Dermal:

Exposure to Liquid
High End: 4.5E+2 mg/day over 247 days/yr
Number of workers (all sites) with Dermal exposure: 192
Basis: Unloading Liquid Raw Material from Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

Dermal:

Exposure to Mist
Output 1: 3.9E+3 mg/day over 247 days/yr
Number of workers (all sites) with Dermal exposure: 1992
Basis: Exposure During Metalworking Operation; User-defined Dermal Model. The 2011 ESD for MWF Operations estimates an average dermal surface loading rate for MWFs of 2.9 mg/cm2-hr during metalworking operations. These data are more conservative than the EPA/OPPT 2-Hand Dermal Contact Model and are used to provide a conservative estimate of dermal exposure during MWF use due to uncertainty at downstream operations. CEB conservatively assessed straight oil where Fchem_trough = Fchem_neat

P-12-0453
Post Focus Review Draft 10/19/2016

This section provides details on EPA's original engineering assessment of occupational exposure and environmental releases from 2012 as well as the Expanded EPA assessment from 2016.  

ENGINEER: Macek
PV (kg/yr): 2,546,302 Import Only 

Revision Notes/Assessment Overview: 06/29/16 Update: This IRER was revised to utilize the methodologies from 2 CP assessments in 2015. Industry comments were also used in this assessment. Changes include: providing several release scenarios for all uses (using WWT removal efficiencies of 50, 70 and 99% as well as assuming monthly and quarterly release of container residuals per industry practices). Occupational assessments remained the same as in the previous version of this IRER. However, dermal assessments inceases as a result of a larger hand surface area used as default in dermal exposure calculations.  The remaining portion of this provides information from the previous assessment. ***  The assessment of this PMN is based on data provided by the submitter as well as data that was collected during EPA previous efforts to assesses environmental releases and occupational exposures during the manufacturing, processing, and use of MCCPs and LCCPs. Additional literature sources that have been reviewed include: 1) previous EPA assessments on chlorinated paraffins; 2) foreign risk assessments on MCCPs and LCCPs (e.g. EU risk assessments); 3) EPA/OPPT Generic Scenarios; 4) OECD Emission Scenario Documents; and 5) Toxics Release Inventory data. Data provided by the submitter, data identified in the literature review, and EPA/OPPT standard models were reviewed and the best available data were used to assesses environmental releases and occupational exposures.

SUBMITTER: Ineos

USE: 1) Seventeen percent (17%) of the notification substances are used as a flame retardant/plasticizer in polymers.  Typical concentration in the plastic is 15%. 2)  Seventy-four percent (74%) of the notification substance is used as a lubricant in metal working fluids (MWFs). The notification substance is blended into the MWFs at 15%. 3)  Two percent (2%) of the notification substances is used as lubricants in sealants (formulated at 10%); and finally 4) Seven percent (7%) of PV is used as plasticizer in adhesives at about 20% formulation.

OTHER USES: Generic uses MCCP based on open lit & other PMN submissions: 1) used as lubricants in automotives. The notification substance i blended into the lubricant at 4%.  [20% consumer uses]. 2)  used as a flame retardant/plasticizer in rubber.  Typical total concentration of flame retardant/plasticizer in the rubber is 1-10%, 3) used as a plasticizer in solvent based paints, adhesives and sealants.  The paints can be specialty paints for applications where weather resistant coatings are needed, such as steel construction, industrial flooring, road marking, and swimming pools. Often blended into the paints at 5-15%.  4) One-half of one percent of the notification substances are applied as a flame retardants/waterproofers to textiles.  Can be at 5% of the textile coating finishing solution.

MSDS:  Yes										LABEL: No

Gen Eqpt: If prolonged or excessive skin contact is likely: Wear suitable protective clothing and gloves. // If splashing or mist is likely to occur: Wear eye/face protection.
Respirator: No information provided.
Health Effects: Eye: Contact with eyes may cause irritation // Skin: Unlikely to cause skin irritation // Inhalation: Unlikely to be hazardous by inhalation. // Ingestion: Unlikely to be hazardous if swallowed. // Chronic Effects: repeated exposure to high levels may produce live and kidney damage.
TLV/PEL: - none established

CRSS:
Chemical Name: Alkanes, C14-17, chloro
S-H2O: 0.00003 g/L @
VP: 2.0E-5 torr @
MW: 336 %<500 %<1000
Physical State and Misc CRSS Info: Neat: liquid	Mfg: liquid
Proc/Form: variable	End Use: 5 - 20% in final product. The average molecular formula would range from C14H26Cl4  ( LOWWT at  ~40% chlorination) to C17H26Cl10 high wt (at ~ 60% chlorination). C# : % (range)  C14: 36 (30-40); C15: 30 (25-35); C16: 24 (20-30); and C17: 10 (8-18)  ChemSpider EPI est for 1,2-dichlorotetradecane : BP  339  / VP  < 1 E-3 mm Hg / s-H2O  < 6  E-6 g/L P-Chem values reported are est / measured supplied by INEOS

Consumer Use: No

SAT (concerns):

Related Cases and Misc SAT Info:
SAT data not yet available
Migration to groundwater: 
PBT rating: PBT SAT data not yet available
Health: 
Eco: 

OCCUPATIONAL EXPOSURE RATING: 2-3D

NOTES & KEY ASSUMPTIONS:
06/29/16 Update: This IRER was revised to utilize the methodologies from 2 CP assessments completed in 2015. Industry comments were also used in this assessment. Changes include: providing several release scenarios for all uses (using WWT removal efficiencies of 50, 70 and 99% as well as assuming monthly and quarterly release of container residuals per industry practices). Occupational assessments remained the same as in the previous version of this IRER. However, dermal assessments increase as a result of a larger hand surface area used as default in dermal exposure calculations.  The remaining portion of this provides information from the previous assessment. Generated by the 09/30/2013 version of ChemSTEER. *** This PMN is a MCCP product that is imported and used in the following applications: 1) 16.8%as a plasticizer in PVC production 2) 8.3 % as a lubricant in metal working fluids (MWFs) 3) 7.4% used in adhesives and 4) 2% used in sealants // Note, the SAT information is not yet available for this PMN. // For downstream processing and use operations: The releases estimates were based on a combination of submitter provided data and data available in various literature sources.  The literature sources include those previously reviewed by EPA as well as Generic Scenarios and Emission Scenario Documents. Many of the sources reviewed by EPA were also provided by the submitter (2005 EU RA on MCCPs, 2010 CSR). Due to the uncertainty at multiple downstream use sites, the most conservative data were chosen when evaluating releases for downstream operations. This assessment approach is consistent with the approached used for previous standard reviews of chlorinated paraffin products including P12‑0277 through P12‑0284, P12‑0357, and P12‑0433. This assessment includes adhesive and sealant formulation and use which is a use that was not listed in the previous assessments. The formulation of adhesives/sealants assessment was based on information provided in sources from the submitter and the 2009 ESD for the Formulation of Adhesives. The end use of adhesives/sealants was based on the 2008 ESD for the Use of Adhesives. // Note, all exposure‑based criteria were met.

POLLUTION PREVENTION CONSIDERATIONS:

EXPOSURE-BASED REVIEW: Yes	(3 criteria met)

 # of workers exposed: 13,834 >1000? Yes
 >100 workers with >10 mg/day inhalation exposure: Yes
 (a) >100 workers w/1-10 mg/day inh. exp. & >100 days/yr: Yes
 (b) Routine Dermal Cont: >250 workers & >100 days/yr: Yes

PROC1: Formulation of Metalworking Fluids (73.8% of PV) 
Number of Sites/Location: 59 sites
unknown site(s)

Basis: The submission does not provide information on the number of customers and or use rate of the PMN in MWF formulation. The submission states that the PMN is formulated in MWFs at a conc of 10-20% for neat oils and 5% for emulsions. Based on different-submitter, same-use past case P12-0280 for the same PMN substance, 110 formulation sites were estimated for a production volume of 3,524,972 kg/yr. Using this as a basis, CEB estimates the number of formulation sites for a PV of 1,879,171 kg/yr as (1,878,171/3,524,972) * 110 ~ 59 sites. CEB assumes at least a 500 gallon mixing vessel to estimate daily throughput of PMN chemical of 378 kg and 84 days/yr. Process Description: PMN (liquid, 100%) is unloaded from import containers ---> feed into blending tank ---> blending ---> packaging of metal working fluids containing PMN (10 - 20% for neat oils, 5% for emulsions) (submission, CRSS, previous Std Review past cases for MCCPs)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The releases estimates were based on a combination of submitter provided data and data available in various literature sources. A description of the data is provided in the release notes for each source. Due to the uncertainty at multiple downstream use sites, the most conservative data were chosen when evaluating releases for downstream operations.

2012 EPA Assessment
Water or Incineration or Landfill
High End: 1.1E+1 kg/site-day over 84 day/yr from 59 sites 
to: uncertain
2016 Expanded EPA Assessment (Oil-based fluids)
Water or Incineration or Landfill
Monthly: 7.8E+1 kg/site-day over 12 day/yr from 30 sites 
Quarterly: 2.2E+2 kg/site-day over 4 day/yr from 30 site
to: Uncertain
2016 EPA Expanded Assessment (water based, on-site pretreatment with 50% efficiency)
Water or Incineration or Landfill
Monthly: 3.9E+1 kg/site-day over 12 day/yr from 30 sites 
Quarterly: 1.2E+2 kg/site-day over 4 day/yr from 30 site
to: Pretreatment (50% removal efficiency) then to POTW, incineration or landfill
2016 EPA Expanded Assessment (water based, on-site pretreatment with 70% efficiency)
Water or Incineration or Landfill
Monthly: 2.3E+1 kg/site-day over 12 day/yr from 30 sites 
Quarterly: 7.0E+1 kg/site-day over 4 day/yr from 30 site
to: Pretreatment (70% removal efficiency) then to POTW, incineration or landfill
2016 EPA Expanded Assessment (water based, on-site pretreatment with 99% efficiency)
Water or Incineration or Landfill
Monthly: 7.8E-1 kg/site-day over 12 day/yr from 30 sites 
Quarterly: 2.3E+0 kg/site-day over 4 day/yr from 30 site
to: Pretreatment (99% removal efficiency) then to POTW, incineration or landfill
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: EPA/OPPT Drum Residual Model, CEB standard 3% residual. The submission does not provide an estimate for releases from drum residuals. Due to uncertainty at multiple downstream sites, CEB assesses releases to uncertain media using the EPA/OPPT Drum residual model.
2016 EPA Expanded Assessment (oil based fluids): Assumes quarterly or monthly container cleaning, per industry information indicating containers are not picked up daily by a waste handler.
2016 EPA Expanded Assessment (water based, on-site pretreatment with 50%, 70% and 99% efficiency): Assumes quarterly or monthly container cleaning, per industry information indicating containers are not picked up daily by a waste handler. Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2014 EPA Assessment
Water or Incineration or Landfill
Conservative: 7.6E+0 kg/site-day over 84 day/yr from 59 sites
to: Uncertain
2016 Expanded EPA Assessment (Oil-based fluids)
Incineration or Landfill
Conservative: 1.3E+0 kg/site-day over 240 day/yr from 30 sites 
to: Incineration or Landfill (industry comments)
2016 Expanded EPA Assessment (water-based, on-site pretreatment with 50% efficiency)
Water or Incineration or Landfill
Conservative: 6.5E-1 kg/site-day over 240 day/yr from 30 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (water-based, on-site pretreatment with 70% efficiency)
Water or Incineration or Landfill
Conservative: 3.9E-1 kg/site-day over 240 day/yr from 30 sites 
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (water-based, on-site pretreatment with 99% efficiency)
Water or Incineration or Landfill
Conservative: 1.3E-2 kg/site-day over 240 day/yr from 30 sites 
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Equipment Cleaning Losses of Liquids from a Mixing Tank
basis: EPA/OPPT Multiple Process Vessel Residual Model, CEB standard 2% residual. The submission does not provide an estimate for releases from equipment cleaning. Due to uncertainty at multiple downstream sites, CEB assesses releases to uncertain media using the EPA/OPPT Multiple Vessel Model.
2016 EPA Expanded Assessment (Oil-Based Fluids):  Industry information indicates cleaning of equipment that is in contact with MCCPs would not use water.  Therefore, wastes are assumed to incineration or landfill.  
2016 EPA Expanded Assessment (water based, on-site pretreatment with 50%, 70% and 99% efficiency):  Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

Air
Output 2: 1.9E-1 kg/site-day over 84 day/yr from 59 sites 
to: fugitive air (2005 EU RA from submission, 2010 Japan RA)
from: Fugitive Air Emissions
basis: User-Defined Loss Rate Model. Data from a 2005 EU RA for MCCP provide by the submitter estimates 16 kg/yr of MCCP may be released to air from fugitive air emissions generated by preheating and blending at a typical MWF formulation site (16kg/yr / 31,850 kg/site-yr = 0.05% for the current operations). A 2010 Japanese RA for SCCPs suggests 0.005% release to air during MWF formulation. Due to uncertainty at multiple downstream use sites, CEB includes this release source using the high end estimate based on the 2005 EU RA.

Incineration or Landfill
Output 2: 7.6E+0 kg/site-day over 84 day/yr from 59 sites 
to: incineration or landfill (2005 EU RA from submission)
from: Off-Spec Material
basis: User-Defined Loss Rate Model. Data from a 2005 EU RA for MCCPs provided by the submitter estimates a 1-2% loss rate from disposal of off-spec batches released to solid waste. Due to uncertainty at multiple downstream use sites, CEB includes this release source using the high end estimate with releases to incineration or landfill.

RELEASE TOTAL

2012 EPA Assessment: 1.3E+5 kg/yr - all sites
2016 EPA Expanded Assessment (Oil-Based Fluids): 5.6E+4 kg/yr - all sites
2016 EPA Expanded Assessment (water-based, on-site pretreatment with 50% efficiency): 3.8E+4 kg/yr - all sites
2016 EPA Expanded Assessment (water-based, on-site pretreatment with 70% efficiency): 3.0E+4 kg/yr - all sites
2016 EPA Expanded Assessment (water-based, on-site pretreatment with 99% efficiency): 1.9E+4 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 472
Basis: The submission does not provide an estimate for the number of workers/site. Previous related submissions (P-12-0277 to P-12-0284) indicated 4 to 8 workers per site.  CEB assumes 8.

Inhalation:
Negligible due to low vapor pressure (VP < 0.001 torr) and physical state as handled (liquid).  

Dermal:

Exposure to Liquid
High End: 2.2E+3 mg/day over 84 days/yr
Number of workers (all sites) with Dermal exposure: 472
Basis: Unloading Liquid Raw Material from Totes and Tank Trucks; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

Dermal:

Exposure to Liquid
High End: 4.5E+2 mg/day over 84 days/yr
Number of workers (all sites) with Dermal exposure: 472
Basis: Loading Liquid Product into Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

PROC2: PVC Compounding (16.8% of PV) 
Number of Sites/Location: 8
unknown site(s)

Days/yr: 126

Basis: Per submission, PMN is used at 100% and is present in compounded PVC at 15%. Estimates for a series of recent related cases (P-12-0277 to P-12-0284) estimated an average of 54,000 kg of chlorinated paraffin per site-yr for this use category.  CEB estimates 8 use sites based on this data.  These same cases also estimated an average kg/site-day for the chlorinated paraffin of 425.7 kg/site-day. Based on the PV for this use category, 8 sites and 425.7 kg/site-day, CEB estimates 126 days/site-yr.
Process Description: PMN (liquid, 100%) is unloaded from transport containers into feeder ---> feed into mechanical mixer ---> extrusion, injection molding, calendaring or other process to form compounded shapes (i.e. pellets, sheets) ----> PMN (solid, 15%) charged to bulk container (GS)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The releases estimates were based on a combination of submitter provided data and data available in various literature sources. A description of the data is provided in the release notes for each source. Due to the uncertainty at multiple downstream use sites, the most conservative data was chosen when evaluating releases for downstream operations.

Water
High End: 4.3E-3 kg/site-day over 126 day/yr from 8 sites 
to: water or air (GS)
from: Fugitive Air Emission During High Temperature Extrusion
basis: User-Defined Loss Rate Model. The 2004 GS for Plastics Compounding estimates a loss rate of 0.002% to fugitive air for low volatility substances which would include MCCP substances. 50% of the releases are expected to remain in the air while the other 50% is expected to be released to water.

2012 EPA Assessment
Water or Incineration
Output 1: 8.5E+0 kg/site-day over 126 day/yr from 8 sites
to: water or incineration (GS)
EPA 2016 Expanded Assessment
Incineration or Landfill
Conservative: 8.5E+0 kg/site-day over 126 day/yr from 8 sites
to: incineration or Landfill (industry comment)
from: Equipment Cleaning Losses of Liquids, from Compounding Equipment
basis: User-Defined Loss Rate Model. The 2004 GS for Plastics Compounding estimates a loss rate of 2% based on the EPA/OPPT Multiple Vessel Residual model with releases to water.
EPA 2016 Expanded Assessment: Assesses release to incineration or landfill, per industry information.

2012 EPA Assessment
Water or Incineration or Landfill
Output 1: 1.3E+1 kg/site-day over 126 day/yr from 8 sites
to: water, incineration or land (GS)
EPA 2016 Expanded Assessment
Water or Incineration or Landfill
Monthly: 1.3E+2 kg/site-day over 12 day/yr from 8 sites 
Quarterly: 4.0E+2 kg/site-day over 4 day/yr from 8 sites 
to: Water or Incineration or Landfill (GS)
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: User-Defined Loss Rate Model. The 2004 GS for Plastics Compounding estimates a loss rate of 3% based on the EPA/OPPT Drum Residual model with releases to water, incineration, or landfill.
EPA 2016 Expanded Assessment: Assumes quarterly or monthly container cleaning, per industry information indicating containers are not picked up daily by a waste handler.

Water or Incineration or Landfill
High End: 4.3E-2 kg/site-day over 126 day/yr from 8 sites
to: water, incineration, or landfill (submission, GS)
from: Spillage During Raw Material Handling
basis: User-Defined Loss Rate Model. A 2005 EU RA for MCCPs provided by the submitter and the 2004 GS for Plastic Compounding estimates a loss rate of 0.01% from spillage during raw material handling with releases to water, incineration, or landfill.

Air
High End: 4.3E-3 kg/site-day over 126 day/yr from 8 sites 
to: water or air (GS)
from: Fugitive Air Emission During High Temperature Extrusion
basis: User-Defined Loss Rate Model. The 2004 GS for Plastics Compounding estimates a loss rate of 0.002% to fugitive air for low volatility substances which would include MCCP substances. 50% of the releases are expected to remain in the air while the other 50% is expected to be released to water.

RELEASE TOTAL

2012 EPA Assessment: 2.1E+4 kg/yr - all sites
EPA 2016 Expanded Assessment: 2.2E+4 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 192
Basis: The submission estimates up to 3 worker/site. The GS for Plastic Compounding estimates up to 24 workers/site.

Inhalation:

Exposure to Particulate
High End of Range: 4.4E+0 mg/day over 126 days/yr
Low End of Range: 3.0E-2 mg/day over 126 days/yr
Number of workers (all sites) with Inhalation exposure: 192
Basis: Fugitive Air Emission During High Temperature Extrusion; User-defined Inhalation Model. The 2004 GS for Plastics Compounding suggests that inhalation exposure is negligible for non-volatile substances during compounding. A 2008 EU Risk Assessment on MCCP provided by the submitter contains monitoring data from plastic compounding operations is the EU. The monitoring data is based on 32 air samples from 4 sites. Results showed MCCP air concentrations ranging from <0.003 to 0.44 mg/m3 with a median of 0.03 mg/m3 and a 90th percentile of 0.15 mg/m3. It is unknown whether these data represent area or personal monitoring data. As conservative, exposures estimates are presented based on the low and high of the range for these data.

INHALATION MONITORING DATA REVIEW

 Uncertainty (estimate based on model, regulatory limit, or data not specific to industry): Yes
 (a) Exposure level >1 mg/day? Yes
   (b) Hazard Rating for health of 2 or greater? No
Inhalation Monitoring Data Desired? Yes (both criteria met)

Dermal:

Exposure to Liquid
High End: 2.2E+3 mg/day over 126 days/yr
Number of workers (all sites) with Dermal exposure: 192
Basis: Unloading Liquid Raw Material from Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

PROC3: Formulation of Adhesives and Sealants (9.4% of PV) 
Number of Sites/Location: 3 sites
unknown site(s)
Days/yr: 200
Basis: The submission estimates 5% PMN in adhesives and 10-30% in sealants. The 2009 ESD for the Formulation of Adhesives an adhesive production rate of 17,000,000 kg/site-yr for large sites and 1,600,000 kg/site-yr for small sites. CEB assumes small sites based on production volume of PMN. Assuming 5% conc to maximize the number of sites, the ESD estimates the number of formulation sites as: (236,352 kg/yr) / (1,600,000 kg/site-yr x 0.05) ~ 3 sites. The ESD also estimates the number of batches as follows: 1,600,000 kg/site-yr / 4,000 kg/bt = 400 bt/yr. CEB assumes 30% conc in product to conservatively assess exposures. CS calculates a use rate of 199.46 kg/bt.
Process Description: PMN (liquid, 100%) unloaded from containers ---> transfer to mixing vessel ---> mixing assuming unsealed process ---> PMN (5% in adhesives, 10-30% in sealants) packaged for shipment to customers (ESD)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The releases estimates were based on a combination of sources provided by the submitter and estimates from the 2009 ESD for Adhesive Formulation. Due to the uncertainty at multiple downstream use sites, the most conservative data were chosen when evaluating releases for downstream operations.
2016 EPA Expanded Assessment: Based on industry comments, releases to uncertain as well as releases to wastewater treatment (wastewater treatment efficiencies of 50, 70, and 99%) have been assessed.

EPA 2012 Assessment 
Water or Incineration or Landfill
High End: 1.2E+1 kg/site-day over 200 day/yr from 3 sites 
to: Water or Incineration or Landfill (ESD)
2016 Expanded EPA Assessment (50% on-site pretreatment)
High End: 6.0E+0 kg/site-day over 200 day/yr from 3 sites 
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (70% on-site pretreatment)
High End: 3.6E+0 kg/site-day over 200 day/yr from 3 sites 
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (99% on-site pretreatment)
High End: 1.2E-1 kg/site-day over 200 day/yr from 3 sites 
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: EPA/OPPT Drum Residual Model, CEB standard 3% residual. The 2009 ESD for Adhesive Formulation assesses container residuals to uncertain media using the drum residual model.
2016 EPA Expanded Assessment (on-site pretreatment with 50%, 70% and 99% efficiency): Industry information indicates discharge to POTW would first be pretreated  -  50 - 99% efficiency. This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).

EPA 2012 Assessment 
Water or Incineration or Landfill
Conservative: 8.0E+0 kg/site-day over 200 day/yr from 3 sites
to: Water or Incineration or Landfill (submission, GS)
2016 Expanded EPA Assessment (50% on-site pretreatment)
Conservative: 4.0E+0 kg/site-day over 200 day/yr from 3 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill (2005 EU RA from the submitter, ESD, and industry comments)
2016 Expanded EPA Assessment (70% on-site pretreatment)
Conservative: 2.4E+0 kg/site-day over 200 day/yr from 3 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill (2005 EU RA from the submitter, ESD, and industry comments)
2016 Expanded EPA Assessment (99% on-site pretreatment)
Conservative: 8.0E-2 kg/site-day over 200 day/yr from 3 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill (2005 EU RA from the submitter, ESD, and industry comments)
from: Equipment Cleaning Losses of Liquids from a Mixing Tank
basis: User-Defined Loss Rate Model. A 2005 EU RA for MCCPs provided by the submitter estimates a loss rate of up to 5% from equipment cleanout with releases to incineration or landfill. The 2009 ESD for Adhesives Formulation assesses equipment cleaning wastes to uncertain media using a 2% loss fraction.
2016 EPA Expanded Assessment (on-site pretreatment with 50%, 70% and 99% efficiency): Industry information indicates discharge to POTW would first be pretreated  -  50 - 99% efficiency. This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).

Water or Incineration or Landfill
Output 2: 2.0E+2 kg/site-day over 4 day/yr from 3 sites
to: water, incineration, or landfill (ESD)
from: Off-Spec Material
basis: User-Defined Loss Rate Model. The 2009 ESD for Adhesive Formulation estimates releases from off-spec batches with 1% of batches being off-spec and released to water, incineration, or landfill. This is equal to (400 bt/site-yr x 0.01) = 4 bt/yr. At 199.46 kg/bt and 1 off-spec bt/day, it is assumed that 199.46 kg/site-day will be released over 4 days/yr.

RELEASE TOTAL

2012 EPA Assessment: 1.4E+4 kg/yr - all sites
2016 EPA Expanded Assessment (on-site pretreatment with 50% efficiency): : 8.4E+3 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 66
Basis: The 2009 ESD for Adhesive Formulation estimates 22 workers/site exposed during formulation.

Inhalation:
Negligible due to low vapor pressure (VP < 0.001 torr) and physical state as handled (liquid).  

Dermal:

Exposure to Liquid
High End: 2.2E+3 mg/day over 5 days/yr
Number of workers (all sites) with Dermal exposure: 66
Basis: Unloading Liquid Raw Material from Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

Dermal:

Exposure to Liquid
High End: 5.3E+2 mg/day over 34 days/yr
Number of workers (all sites) with Dermal exposure: 66
Basis: Loading Liquid Product into Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

USE1: Use of Metalworking Fluids 73.8% of PV)
Number of Sites/Location: 207 sites .
unknown sites

Days/yr: 247 

Basis: The submission does not provide an estimate for the number of metalworking fluid use sites. The 2011 ESD for MWF Operations estimates 247 days/yr of operation. The Assuming 20% PMN in MWF, the ESD estimates the number of sites as: (1,879,171 kg/yr) / (12,000 gal/site-yr x 1 kg/L x 3.785 L/gal x 0.2) = 207 sites. Environmental releases are of concern for this PMN. As conservative, CEB assumes 247 days/yr of operation and the ESD estimate of 207 sites to maximize kg/site-day release. CEB assumes up to 20% PMN in raw material for straight oils.  Per ESD, straight oils are not expected to be diluted prior to MWF use; therefore, CEB assumes 20% PMN during use to maximize exposure to mist. CS calculates 36.7535 kg/site-day.
Process Description: Bulk MWF containing PMN (liquid, 10-20% for neat oils, 5% for emulsions) is unloaded from transport containers ---> transfer to mixing vessel ---> dilution of MWF ---> diluted MWF containing PMN (liquid, 10-20% for straight oil, assume 10-fold dilution for water-based emulsions, 0.5%) transferred to metal shaping trough ---> metal shaping operation ---> shaped metal part is rinsed and dried ---> spent MWF is drained and discarded (submission, ESD)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The releases estimates were based on a combination of submitter provided data and data available in various literature sources. A description of the data is provided in the release notes for each source.  Due to the uncertainty at multiple downstream use sites, the most conservative data were chosen when evaluating releases for downstream operations.

2012 EPA Assessment
Water or Incineration or Landfill
High End: 1.2E+0 kg/site-day over 218 day/yr from 207 sites 
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Oil-Based Fluids)
Incineration or Landfill
High End: 1.2E+0 kg/site-day over 18 day/yr from 292 sites
to: incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water, Incineration or Landfill
High End: 6.2E-1 kg/site-day over 77 day/yr from 292 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water, Incineration or Landfill
High End: 3.7E-1 kg/site-day over 77 day/yr from 292 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water, Incineration or Landfill
High End: 1.2E-2 kg/site-day over 77 day/yr from 292 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: EPA/OPPT Drum Residual Model, CEB standard 3% residual. The 2011 ESD for MWF Operations estimates releases using the EPA/OPPT drum residual model (3% loss rate) with releases to water, incineration, or landfill. Due to uncertainty at multiple downstream sites, these releases are assessed to uncertain media using a 3% loss rate.
2016 Expanded EPA Assessment (Oil-Based Fluids): 2011 OECD ESD for Use of Metalworking Fluids assesses spend metalworking fluids for oil-based fluids to incineration or landfill:  
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency). Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water
Output 2: 3.9E+0 kg/site-day over 247 day/yr from 207 sites
to: on-site WWTP or POTW (ESD)
2016 Expanded EPA Assessment (Oil-Based Fluids)
Water or Incineration or Landfill
Output 2: 1.4E+0 kg/site-day over 247 day/yr from 292 sites 
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water
High End: 7.0E-1 kg/site-day over 247 day/yr from 292 sites
to: on-site WWTP or POTW (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water
High End: 4.2E-1 kg/site-day over 247 day/yr from 292 sites
to: on-site WWTP or POTW (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water
High End: 1.4E-2 kg/site-day over 247 day/yr from 292 sites
to: on-site WWTP or POTW (ESD)
from: Dragout Losses
basis: User-Defined Loss Rate Model. The 2011 ESD for MWF Operations estimates workpiece dragout to account for 1 to 2% with releases water or chemical waste and grinding swarf dragout is estimated to be 30 to 90% with releases to incineration or landfill. A 2010 EU CSR for MCCPs estimates overall process losses to be 1 to 6% with releases to water. The 2011 ESD for MWF Operations estimates a loss rate of 11% from dragout with releases to on-site WWTP or POTW. These data are based on U.S. industry data collected during the development of effluent guidelines for the metalworking industry. These data provide the best representation of U.S. operations and are more conservative than the submitter estimates. Due to uncertainty at multiple downstream sites, CEB assesses dragout releases using the ESD estimate of 11% and accounting for upstream losses from container cleaning: (1-0.03) x 0.11 = 0.1067. Releases are assessed to water via on-site WWTP or POTW per submission and ESD.
2016 Expanded EPA Assessment¨ 2011 OECD ESD for Use of Metalworking Fluids assesses dragout losses of metalworking fluids for oil-based fluids to water, incineration or landfill. 
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency).  Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water or Incineration or Landfill
Output 2: 1.3E+1 kg/site-day over 247 day/yr from 207 sites
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Oil-Based Fluids)
Incineration or Landfill
Output 2: 4.5E+0 kg/site-day over 247 day/yr from 292 sites
to: incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water, Incineration or Landfill
High End: 2.3E+0 kg/site-day over 247 day/yr from 292 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water, Incineration or Landfill
High End: 1.4E+0 kg/site-day over 247 day/yr from 292 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water, Incineration or Landfill
High End: 4.5E-2 kg/site-day over 247 day/yr from 292 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Filter Media and Other Recycling Waste
basis: User-Defined Loss Rate Model. The submission does not address releases from recycling or filter media losses. The 2011 ESD for MWF Operations estimates these releases to account for a 36% loss rate with releases to water, incineration, or landfill (water-based fluids) or incineration or landfill (straight-oil). Accounting for upstream container cleaning losses: (1-0.03) x 0.36 = 0.3492. CEB assesses these releases to water, incineration, or landfill based on uncertainty at multiple downstream use sites.
2016 Expanded EPA Assessment (Oil-Based Fluids) 2011 OECD ESD for Use of Metalworking Fluids assesses disposal of filter media and other recycling waste to incineration or landfill for oil-based fluids. 
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency). Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Water or Incineration or Landfill
Output 2: 1.6E+1 kg/site-day over 247 day/yr from 207 sites
to: water, incineration, or landfill (ESD)
2016 Expanded EPA Assessment Oil-Based Fluids)
Incineration or Landfill
Output 2: 6.7E+0 kg/site-day over 247 day/yr from 292 sites
to: incineration, or landfill (ESD)
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment)
Water, Incineration or Landfill
High End: 3.4E+0 kg/site-day over 247 day/yr from 292 sites
to: Pretreatment (50% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment)
Water, Incineration or Landfill
High End: 2.0E+0 kg/site-day over 247 day/yr from 292 sites
to: Pretreatment (70% efficiency) then to POTW, incineration or landfill
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment)
Water, Incineration or Landfill
High End: 6.7E-2 kg/site-day over 247 day/yr from 292 sites
to: Pretreatment (99% efficiency) then to POTW, incineration or landfill
from: Spent Metalworking Fluid
basis: User-Defined Loss Rate Model. The submission assesses the remaining fluid to POTW from spent MWF disposal with bath changeouts occurring 5 times/yr. The 2011 ESD for MWF Operations also assesses 100% release with the spent MWF disposed to water (water-based fluids) or incineration or landfill (straight oil fluids) with at least one bath changeout occurring per day at a facility with multiple baths in use. Based on uncertainty at multiple downstream use sites, CEB assesses the spent MWF to water, incineration, or landfill. Account for upstream losses, the loss rate is calculated as: (1-0.03) x (1-0.05-0.11-0.38) = 0.4462.
2016 Expanded EPA Assessment (Oil-Based Fluids) 2011 OECD ESD for Use of Metalworking Fluids assesses disposal of spent metalworking fluid to incineration or landfill for oil-based fluids.  
2016 Expanded EPA Assessment (Water-Based Fluids with on-site pretreatment with 50%, 70% and 99% efficiency). Industry information indicates facilities must meet O&G limits.  Discharge to POTW would first be pretreated  -  50 - 99% efficiency.  This presents release to POTW (with pretreatment 50%, 70% and 99% removal efficiency).  

2012 EPA Assessment
Air
Output 2: 1.8E+0 kg/site-day over 247 day/yr from 207 sites 
to: air (2005 EU RA from submission)
from: Misting/Evaporation
basis: User-Defined Loss Rate Model. A 2005 EU RA for MCCP provided by the submitter estimates misting/evaporation losses to range from 2 to 5% depending on the type of MWF begin used. Based on uncertainty at multiple downstream sites, CEB uses the most conservative estimate of 5% loss to air from misting/evaporation. Account for upstream losses from container cleaning: (1-0.03) x 0.05 = 0.0485.
EPA 2016 Expanded Assessment: This release source was removed.

RELEASE TOTAL

2012 EPA Assessment: 1.8E+6 kg/yr - all sites
2016 Expanded EPA Assessment (Oil-Based Fluids): 9.2E+5 kg/yr - all sites
2016 Expanded EPA Assessment (Water-Based Fluids, 50% on-site pretreatment): 4.7E+5 kg/yr - all sites
2016 Expanded EPA Assessment (Water-Based Fluids, 70% on-site pretreatment): 2.8E+5 kg/yr - all sites
2016 Expanded EPA Assessment (Water-Based Fluids, 99% on-site pretreatment): 9.4E+3 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 9,936
Basis: The 2011 ESD for MWF Use estimates 48 workers/site. 

Inhalation:

Exposure to Mist
High End of Range: 7.1E+0 mg/day over 247 days/yr
Typical: 2.0E+0 mg/day over 247 days/yr
Number of workers (all sites) with Inhalation exposure: 9,936
Basis: Exposure During Metalworking Operation; User-defined Inhalation Model. A 2005 EU RA for MCCPs provided by the submitter estimates mist concentrations from 1.6 to 3.4 mg/m3 based on the 95th percentile of data collected in the EU for oil-based and water-based fluids. The data from the 2011 ESD are more representative of U.S. operations since the data were collected in the U.S. The 2011 ESD for MWF Operations estimates typical mist concentrations ranging from 0.19 to 0.39 mg/m3 and high end concentrations ranging from 0.87 to 1.42 mg/m3 depending on the type of MWF used. These estimates are based on the geometric mean (typical) and 90th percentile data (high end) of data collected by NIOSH from 942 machinists at 79 shops across the U.S. A range of inhalation exposure estimates are based the high end for the range of geometric means and 90th percentiles. For water-based fluids, the PMN chemical could be as high as 50% of the mist (20% neat concentration/40% non-water per generic scenario).   Therefore, concentrations are estimated to range from (0.5 x 0.39) = 0.195 mg/m3 to (0.5 x 1.42) = 0.71 mg/m3.

INHALATION MONITORING DATA REVIEW

 Uncertainty (estimate based on model, regulatory limit, or data not specific to industry): Yes
 (a) Exposure level >1 mg/day? Yes
   (b) Hazard Rating for health of 2 or greater? No
Inhalation Monitoring Data Desired? Yes (both criteria met)

Dermal:

Exposure to Liquid
High End: 4.5E+2 mg/day over 247 days/yr
Number of workers (all sites) with Dermal exposure: 9,936
Basis: Unloading Liquid Raw Material from Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

Dermal:

Exposure to Mist
Output 1: 3.9E+3 mg/day over 247 days/yr
Number of workers (all sites) with Dermal exposure: 9,936
Basis: Exposure During Metalworking Operation; User-defined Dermal Model. The 2011 ESD for MWF Operations estimates an average dermal surface loading rate for MWFs of 2.9 mg/cm2-hr during metalworking operations. These data are more conservative than the EPA/OPPT 2-Hand Dermal Contact Model and are used to provide a conservative estimate of dermal exposure during MWF use due to uncertainty at downstream operations. 

USE2: PVC Converting (16.8% of PV) 
Number of Sites/Location: 8
unknown site(s)
Days/yr: 250
Basis: Per submission, the upstream compounding process yields PVC containing 15% PMN. CEB assumes the number of converting sites is equal to the number of compounding sites and estimates up to 250 days/suite-yr to estimate a daily throughput for the PMN chemical of 214 kg/site-day.
Process Description: PVC pellets or other solid form containing PMN (solid, 15%) are unloaded ---> forming (heating) ---> molding and shaping using various processes (injection molding, extrusion, casting, calendaring, etc.) ---> trimming ---> finishing ---> finishing plastic article (GS)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The releases estimates are based data available in various literature sources. A description of the data is provided in the release notes for each source. Due to the uncertainty at multiple downstream use sites, the most conservative data were chosen when evaluating releases for downstream operations.

Water
Output 2: 1.6E-1 kg/site-day over 250 day/yr from 8 sites 
to: Water (50%) or Air (50%) (GS, 2010 CSR and 2005 EU RA provided by the submitter)
from: Fugitive Air Emission During Forming and Molding
basis: User-Defined Loss Rate Model. Data from sources provided by the submitter suggests that fugitive air emissions generated during forming and molding can range between 0.002 to 0.15% with engineering controls depending on the type of conversion process (e.g. extrusion, injection molding, calendaring). The 2004 GS for Plastics Converting estimates that 50% of air emissions will settle and be ultimately released to water while the other 50% remains in air. As conservative, CEB assesses fugitive air emissions at a loss rate of 0.15% with 50% to water and 50% to air.

EPA 2012 Assessment
Water or Incineration or Landfill
Output 2: 2.1E-2 kg/site-day over 250 day/yr from 8 sites
to: water, incineration or landfill (2010 CSR provided by the submitter)
EPA 2016 Expanded Assessment: 
Water or Incineration or Landfill
Output 2: 1.1E-3 kg/site-day over 250 day/yr from 8 sites
to: water, incineration or landfill (RM-2)
from: Raw Material Spillage
basis: User-Defined Loss Rate Model. A 2010 EU CSR assessment on MCCPs provided by the submitter estimated these releases to be 0.01% of PV with releases to water or solid waste (consistent with updated Generic Scenario 2014).
EPA 2016 Expanded Assessment: Industry information indicates use of industrial traps in drains would capture up to 95% of spillage lost to drains before going to water. Both 95% removal and 0% removal efficiencies have been presented.

EPA 2012 Assessment
Water or Incineration or Landfill
Output 2: 2.1E+0 kg/site-day over 250 day/yr from 8 sites 
to: water, incineration or landfill (GS)
EPA 2016 Expanded Assessment
Incineration or Landfill
Output 2: 1.0E+1 kg/site-day over 40 day/yr from 8 sites 
to: incineration or landfill
from: Cleaning Solid/ Powder Residuals from Containers Used to Transport the Raw Material
basis: EPA/OPPT Solid Residuals in Transport Containers Model, CEB standard 1% residual. The 2004 GS for Plastics Converting estimates releases from container cleaning using the EPA/OPPT model for solid residuals with releases to water, incineration, or landfill.
EPA 2016 Expanded Assessment: Converted plastics material considered mostly likely to be handled as solid waste and disposed by landfill or incineration (consistent with updated Generic Scenario 2014).

EPA 2012 Assessment 
Water or Incineration or Landfill
Conservative: 4.3E+0 kg/site-day over 250 day/yr from 8 sites 
to: water, incineration or landfill (GS)
EPA 2016 Expanded Assessment
Incineration or Landfill
Conservative: 4.3E+0 kg/site-day over 250 day/yr from 8 sites 
to: incineration or landfill
from: Equipment Cleaning Losses of Liquids from Multiple Vessels
basis: EPA/OPPT Multiple Process Vessel Residual Model, CEB standard 2% residual. The 2004 GS for Plastics Converting estimates releases from equipment cleaning using the EPA/OPPT model loss rate of 2% with releases to water, incineration, or landfill.
EPA 2016 Expanded Assessment: Converted plastics material considered mostly likely to be handled as solid waste and disposed by landfill or incineration.

EPA 2012 Assessment 
Water or Landfill
Output 2: 5.3E+0 kg/site-day over 250 day/yr from 8 sites 
to: water or landfill (GS)
EPA 2016 Expanded Assessment
Incineration or Landfill
Output 2: 5.3E+0 kg/site-day over 250 day/yr from 8 sites 
to: incineration or landfill 
from: Scrap Material
basis: User-Defined Loss Rate Model. A 1992 RM-2 assessment for SCCPs estimated scrap from trimming to be 1% of the PV with 90% of releases going to landfill. The 2004 GS for Plastics Converting estimated these releases to be 2.5% of PV with releases to water or landfill. This is based on the assumption that large pieces of scrap material will be disposed to landfill via solid waste and dust generated during trimming will settle to the floor and be washed away to wastewater during cleaning. Due to multiple unknown downstream sites, CEB conservatively assesses a 2.5% loss rate with releases to water or landfill based on the GS.
2016 Expanded EPA Assessment:  Scrap material expected to be handled as solid waste and disposed by landfill or incineration.

Air
Output 2: 1.6E-1 kg/site-day over 250 day/yr from 8 sites 
to: Water (50%) or Air (50%) (GS, 2010 CSR and 2005 EU RA provided by the submitter)
from: Fugitive Air Emission During Forming and Molding
basis: User-Defined Loss Rate Model. Data from sources provided by the submitter suggests that fugitive air emissions generated during forming and molding can range between 0.002 to 0.15% with engineering controls depending on the type of conversion process (e.g. extrusion, injection molding, calendaring). The 2004 GS for Plastics Converting estimates that 50% of air emissions will settle and be ultimately released to water while the other 50% remains in air. As conservative, CEB assesses fugitive air emissions at a loss rate of 0.15% (consistent with updated Generic Scenario 2014) with 50% to water and 50% to air.

EPA 2012 Assessment
Air
Output 2: 2.4E-2 kg/site-day over 250 day/yr from 8 sites 
to: air or landfill w/ 99% dust collection efficiency (RM-2)
EPA 2016 Expanded Assessment
Water or Landfill
Output 2: 2.1E-2 kg/site-day over 250 day/yr from 8 sites 
to: water or landfill
from: Dust Generation from Converting
basis: User-Defined Loss Rate Model. A 1992 RM-2 Assessment of SCCPs estimates a loss rate of 75g/kg of plastic produced with 1% of releases to air and 99% to landfill based on a 99% dust collection efficiency. Based on a MCCP concentration of 15%, the loss rate for PMN during plastic converting is 75g/kg of plastic x 0.15 = 11.25 g/kg of plastic, or 1.125%.
EPA 2016 Expanded Assessment: Dust initially to air but expected to settle to ground and be cleaned from equipment and floor with water or disposed directly to landfill.

EPA 2012 Assessment
Landfill
Output 2: 2.4E+0 kg/site-day over 250 day/yr from 8 sites 
to: air or landfill w/ 99% dust collection efficiency (RM-2)
EPA 2016 Expanded Assessment
Water or Landfill
Output 2: 2.1E-2 kg/site-day over 250 day/yr from 8 sites 
to: water or landfill
from: Dust Generation from Converting
basis: User-Defined Loss Rate Model. A 1992 RM-2 Assessment of SCCPs estimates a loss rate of 75g/kg of plastic produced with 1% of releases to air and 99% to landfill based on a 99% dust collection efficiency. Based on a MCCP concentration of 15%, the loss rate for PMN during plastic converting is 75g/kg of plastic x 0.15 = 11.25 g/kg of plastic, or 1.125%.
EPA 2016 Expanded Assessment: Dust initially to air but expected to settle to ground and be cleaned from equipment and floor with water or disposed directly to landfill.

RELEASE TOTAL

EPA 2012 Assessment: 2.9E+4 kg/yr - all sites
EPA 2016 Expanded Assessment: 2.4E+4 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 384
Basis: Per 2004 GS for Plastics Converting, 48 workers/site.

Inhalation:

Exposure to Particulate
High End of Range: 2.2E+1 mg/day over 250 days/yr
Low End of Range: 1.2E+1 mg/day over 250 days/yr
Number of workers (all sites) with Inhalation exposure: 1,536
Basis: Inhalation Exposure during Converting; User-defined Inhalation Model. A 2005 EU RA on MCCPs and a 2010 EU CSR on MCCPs provided by the submitter contains monitoring data from PVC converting operations is the EU. The monitoring data suggest MCCP air concentrations ranging from <0.01 to 1.2 mg/m3 depending on the type of converting process. These data are based on over 28 samples taken from 4 sites. It is unknown whether these data represent area or personal monitoring data. The 2004 GS for Plastics Converting estimates exposures during converting using the OSHA PEL Limiting Model. Based on uncertainty in multiple downstream use sites and the fact that these data are only based on 1 site, CEB assesses exposures based on the high end of the EU data range (1.2 mg/m3) and the OSHA PEL (15 mg/m3 x 0.15 = 2.25 mg/m3).

INHALATION MONITORING DATA REVIEW

 Uncertainty (estimate based on model, regulatory limit, or data not specific to industry): Yes
 (a) Exposure level >1 mg/day? Yes
    (b) Hazard Rating for health of 2 or greater? No
Inhalation Monitoring Data Desired? Yes (both criteria met)

Dermal:

	PMN will be encapsulated in plastic pellets during handling of plastic raw material. While some surface contact may occur, dermal exposure to solids in this form are non-quantifiable (2004 ESD; Cast Solids, CEB Method for Screening-Level Assessments of Dermal Exposure).

USE3: Use of Adhesives and Sealants (9.4% of PV) 
Number of Sites/Location: 58 sites
unknown sites
Days/yr: 250
Basis: The submission estimates 5% PMN in adhesives and 10-30% in sealants. The 2008 ESD for Adhesives Use estimates a default adhesive use rate of 13,504 kg/site-yr. Assuming 30% conc to maximize the release per site, the number of sites is estimates as: (236,352 kg/yr) / (13,504 kg/site-yr x 0.3) ~ 58 sites which is a reasonable estimate for 3 upstream formulators. The ESD estimates 250 days/yr. CS calculates a use rate of 16.5071 kg/site-day.
Process Description: PMN (5% in adhesive, 10-30% in sealants) unloaded from containers ---> dilute and mix (optional) ---> transfer to application reservoir or apparatus ---> apply adhesive/sealant to substrate ---> drying/curing ---> product finishing (optional) (ESD)

ENVIRONMENTAL RELEASES ESTIMATE SUMMARY

IRER Note: The daily releases listed for any source below may coincide with daily releases from the other sources to the same medium. The 2008 ESD for Adhesives Use is used as a basis for estimating releases from the industrial use of adhesives and sealants.

Water or Incineration or Landfill
High End: 1.9E+0 kg/site-day over 66 day/yr from 58 sites 
to: Water, Incineration or Landfill (ESD)
from: Cleaning Liquid Residuals from Drums Used to Transport the Raw Material
basis: EPA/OPPT Drum Residual Model, CEB standard 3% residual. The 2008 ESD for Adhesives Use estimates releases from container cleaning to uncertain media using the 3% drum residual model.

Water or Incineration or Landfill
Conservative: 3.3E-1 kg/site-day over 250 day/yr from 58 sites
to: Water or Incineration or Landfill (submission, ESD)
from: Equipment Cleaning Losses of Liquids from Multiple Vessels
basis: EPA/OPPT Multiple Process Vessel Residual Model, CEB standard 2% residual. The 2008 ESD for Adhesives Use estimates releases from equipment cleaning to uncertain media using the 2% multiple equipment residual model.

Air
High End: 1.2E+0 kg/site-day over 250 day/yr from 58 sites
to: air (90%) or landfill (10%) (spray model)
from: Application Losses
basis: EPA/OPPT Automobile Refinish Coating Overspray Loss Model (non-volatiles). The submission does not provided information as to the type of end use applications for adhesives and sealants containing the PMN. They only indicate that they are for industrial applications. As conservative, CEB assumes adhesives and sealants will be spray applied and uses the auto refinishing spray model with a transfer efficiency of 25% and a filter capture efficiency of 90% which is consistent with the 2008 ESD for Adhesives Use.

Landfill
High End: 1.1E+1 kg/site-day over 250 day/yr from 58 sites
to: air (90%) or landfill (10%) (spray model)
from: Application Losses
basis: EPA/OPPT Automobile Refinish Coating Overspray Loss Model (non-volatiles). The submission does not provided information as to the type of end use applications for adhesives and sealants containing the PMN. They only indicate that they are for industrial applications. As conservative, CEB assumes adhesives and sealants will be spray applied and uses the auto refinishing spray model with a transfer efficiency of 25% and a filter capture efficiency of 90% which is consistent with the 2008 ESD for Adhesives Use.

RELEASE TOTAL

1.9E+5 kg/yr - all sites

OCCUPATIONAL EXPOSURES ESTIMATE SUMMARY

Tot. # of workers exposed via assessed routes: 2,784
Basis: The most recent version of the ESD for Adhesives Use (2012) estimates 26 to 90 workers/site exposed for depending on end use market. The average for the 5 end use markets covered in the scenario is 48 workers per site.

Inhalation:

Exposure to Mist
What-If: 2.3E+1 mg/day over 250 days/yr
Number of workers (all sites) with Inhalation exposure: 2,784
Basis: Coating Using Hand-Held Spray Gun; EPA/OPPT Automobile Refinish Spray Coating Inhalation Model (non-volatile non-polyisocyanates). The 2008 ESD for Adhesives Use recommends using the automobile OEM spray coating model to assess inhalation exposure during spray coating.

INHALATION MONITORING DATA REVIEW

 Uncertainty (estimate based on model, regulatory limit, or data not specific to industry): Yes
 (a) Exposure level >1 mg/day? Yes
   (b) Hazard Rating for health of 2 or greater? No
Inhalation Monitoring Data Desired? Yes (both criteria met)

Dermal:

Exposure to Liquid
High End: 5.3E+2 mg/day over 250 days/yr
Number of workers (all sites) with Dermal exposure: 2,784
Basis: Unloading Liquid Raw Material from Drums; EPA/OPPT 2-Hand Dermal Contact with Liquids Model.

                                       
 EXPOSURE SCENARIO ESTIMATES
(E-FAST Model Run. SEE APPENDIX G FOR REFERENCE TO FULL REPORTS UNDER SEPARATE COVER)

                          POST-FOCUS EXPOSURE REPORT
This updated assessment is based on the Post-Focus Draft Revision 1 dated 10/19/2016.
	Chemical ID:   P-12-0453	                                                Reviewer: Tobias/EN 
         		  Results Table: Dose, Concentration, and Days Exceeded Results Summary
Exposure Scenario[1]
                                     Water
                                   Landfill
                                   Stack Air
                                 Fugitive Air
Release activity(ies)[2]; exposure calculation(s)[3]
                                Drinking Water
                                Fish Ingestion
                                    7Q10[4]
                                    CC = 1
                               PDM Days Exceeded
                                     LADD
                                      ADR
                                 (24-hr conc.)
                              LADD (Annual conc.
                                      ADR
                                 (24-hr conc.)
                              LADD (Annual conc.

                                      ADR
                                     LADD
                                      ADR
                                     LADD
                                       
                                       
                                       
                                       
                                       
                                       
                                       

                                   mg/kg/day
                                   mg/kg/day
                                   mg/kg/day
                                   mg/kg/day
                                     μg/l
                                    # Days
                                   mg/kg/day
                                   mg/kg/day
                                  (ug/m[3])
                                   mg/kg/day
                                  (ug/m[3])
                                   mg/kg/day
                                  (ug/m[3])
                                   mg/kg/day
                                  (ug/m[3])
PROC1 : Max ADR
                                   6.60E-01
                                      ---
                                   2.17E+01
                                      ---
                                   2.96E+04
                                      ---
                                      ---
                                   2.88E+00
                                  (1.58E+04)
                                      ---
                                   1.63E-03
                                  (8.88E+00)
                                      ---
PROC1: Max LADD
                                      ---
                                   3.50E-04
                                      ---
                                   2.71E-03
                                      ---
                                      ---
                                   2.73E-03
                                       
                                   5.31E-03
                                  (6.86E+01)
                                       
                                   3.62E-05
                                  (4.70E-01)
PROC2: Max ADR
                                   3.40E-01
                                      ---
                                   1.14E+01
                                      ---
                                   1.55E+04
                                      ---
                                      ---
                                   1.52E+00
                                  (8.30E+03)
                                      ---
                                   1.63E-03
                                  (4.70E-01)
                                      ---
PROC2: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   8.38E+01
                                      239
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC2: Max LADD
                                      ---
                                   2.42E-04
                                      ---
                                   1.87E-03
                                      ---
                                      ---
                                   1.85E-03
                                      ---
                                   3.60E-03
                                  (4.65E+01)
                                      ---
                                   3.62E-05
                                  (4.70E-01)
PROC3: Max ADR
                                   2.00E-01
                                      ---
                                   6.65E+00
                                      ---
                                   9.07E+03
                                      ---
                                      ---
                                   9.00E-01
                                  (4.92E+03)
                                      ---
                                   1.63E-03
                                  (4.70E-01)
                                      ---
PROC3: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   5.03E+01
                                      239
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC3: Max LADD
                                      ---
                                   1.42E-04
                                      ---
                                   1.10E-03
                                      ---
                                      ---
                                   1.46E-03
                                      ---
                                   2.85E-03
                                  (3.68E+01)
                                      ---
                                   3.62E-05
                                  (4.70E-01)
PROC4: Max ADR
                                   6.59E-03
                                      ---
                                   2.20E-01
                                      ---
                                   2.98E+02
                                      ---
                                      ---
                                   6.04E-02
                                  (3.30E+02)
                                      ---
                                   1.63E-03
                                  (8.88E+00)
                                      ---
PROC4: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.68E+00
                                      67
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC4: Max LADD
                                      ---
                                   4.69E-06
                                      ---
                                   3.62E-05
                                      ---
                                      ---
                                   9.34E-04
                                      ---
                                   1.82E-03
                                  (2.35E+01)
                                       
                                   3.62E-05
                                  (4.70E-01)
PROC5: Max ADR: max acute eco
                                   2.85E-03
                                      ---
                                   9.44E-02
                                      ---
                                   1.29E+02
                                      ---
                                      ---
                                   2.60E-01
                                  (1.41E+03)
                                      ---
                                      ---
                                      ---
PROC5: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.29E+02
                                      200
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC5: Max LADD
                                      ---
                                   7.61E-05
                                      ---
                                   5.88E-04
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC6: Max ADR: max acute eco
                                   1.10E-01
                                      ---
                                   3.78E+00
                                      ---
                                   5.16E+03
                                      ---
                                      ---
                                   5.00E-01
                                  (2.75E+03)
                                      ---
                                   2.75E-03
                                  (1.50E+01)
                                      ---
PROC6: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.97E+00
                                      41
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC6: Max LADD
                                      ---
                                   6.16E-05
                                      ---
                                   4.76E-04
                                      ---
                                      ---
                                   3.93E-04
                                      ---
                                   7.65E-04
                                  (9.88E+00)
                                      ---
                                   3.21E-05
                                  (4.10E-01)
PROC7: Max ADR: max acute eco
                                   1.71E-03
                                      ---
                                   5.66E-02
                                      ---
                                   7.73E+01
                                      ---
                                      ---
                                   2.50E-01
                                  (1.39E+03)
                                      ---
                                      ---
                                      ---
PROC7: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   7.73E+01
                                      199
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC7: Max LADD
                                      ---
                                   4.57E-05
                                      ---
                                   3.53E-04
                                      ---
                                      ---
                                   2.94E-04
                                      ---
                                   5.71E-04
                                  (7.38E+00)
                                      ---
                                      ---
PROC8: Max ADR: max acute eco
                                   5.71E-02
                                      ---
                                   1.89E+00
                                      ---
                                   2.58E+03
                                      ---
                                      ---
                                   2.50E-01
                                  (1.35E+03)
                                      ---
                                      ---
                                      ---
PROC8: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   2.58E+00
                                      82
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC8: Max LADD
                                      ---
                                   3.20E-05
                                      ---
                                   2.47E-04
                                      ---
                                      ---
                                   1.23E-04
                                      ---
                                   2.40E-04
                                  (3.10E+00)
                                      ---
                                      ---
USE1: Max ADR
                                   1.13E-03
                                      ---
                                   2.20E-02
                                      ---
                                   5.30E+01
                                      ---
                                      ---
                                   1.70E-02
                                  (9.30E+01)
                                      ---
                                      ---
                                      ---
USE1: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   5.30E+01
                                      210
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE1: Max LADD
                                      ---
                                   2.19E-05
                                      ---
                                   1.70E-04
                                      ---
                                      ---
                                   4.60E-04
                                       
                                   8.98E-04
                                  (1.16E+01)
                                      ---
                                      ---
USE2: Max ADR
                                   5.67E-03
                                      ---
                                   1.10E-01
                                      ---
                                   2.66E+02
                                      ---
                                      ---
                                   7.80E-03
                                  (4.26E+01)
                                      ---
                                      ---
                                      ---
USE2: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   2.66E+02
                                      76
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE2: PDM2
                                      ---
                                      ---
                                      ---
                                      ---
                                   2.42E+02
                                      244
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE2:  Max LADD
                                      ---
                                   1.03E-04
                                       
                                   7.99E-04
                                      ---
                                      ---
                                   2.14E-04
                                      ---
                                   4.16E-04
                                  (5.37E+00)
                                      ---
                                      ---
USE3: Max ADR
                                   3.38E-03
                                      ---
                                   6.60E-02
                                      ---
                                   1.59E+02
                                      ---
                                      ---
                                   4.65E-03
                                  (2.54E+01)
                                      ---
                                      ---
                                      ---
USE3: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.59E+02
                                      75
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE3: PDM2
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.45E+02
                                      239
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE3: Max LADD
                                      ---
                                   6.17E-05
                                      ---
                                   4.77E-04
                                      ---
                                      ---
                                   1.28E-04
                                       
                                   2.48E-04
                                  (3.20E+00)
                                      ---
                                      ---
USE4: Max ADR
                                   1.11E-04
                                      ---
                                   2.17E-03
                                      ---
                                   5.23E+00
                                      ---
                                      ---
                                   1.53E-04
                                  (8.40E-01)
                                      ---
                                      ---
                                      ---
USE4: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   5.23E+00
                                      23
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE4: PDM2
                                      ---
                                      ---
                                      ---
                                      ---
                                   4.77E+00
                                      70
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE4: Max LADD
                                      ---
                                   2.03E-06
                                      ---
                                   1.57E-05
                                      ---
                                      ---
                                   4.20E-06
                                      ---
                                   8.21E-06
                                  (1.10E-01)
                                      ---
                                      ---
USE5: Max ADR: max acute eco
                                   4.35E-03
                                      ---
                                   7.50E-02
                                      ---
                                   2.10E+02
                                      ---
                                      ---
                                   2.75E-03
                                  (1.50E+01)
                                      ---
                                   2.93E-02
                                  (1.60E+02)
                                      ---
USE5: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   3.11E+01
                                      186
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE5: Max LADD
                                      ---
                                   1.51E-05
                                      ---
                                   1.16E-04
                                      ---
                                      ---
                                   4.20E-04
                                      ---
                                   3.17E-05
                                  (4.10E-01)
                                      ---
                                   6.95E-04
                                  (8.98E+00)
USE6: Max ADR: max acute eco
                                   8.06E-05
                                      ---
                                   2.45E-03
                                      ---
                                   3.64E+00
                                      ---
                                      ---
                                   2.38E-02
                                  (1.30E+02)
                                      ---
                                   6.75E-03
                                  (3.69E+01)
                                      ---
USE6: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   3.64E+00
                                      104
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE6: Max LADD
                                      ---
                                   2.47E-06
                                      ---
                                   1.91E-05
                                      ---
                                      ---
                                   4.12E-04
                                      ---
                                   7.97E-04
                                  (1.03E+01)
                                      ---
                                   1.56E-04
                                  (2.02E+00)
[1] Exposure scenario titles consist of release activity followed by exposure calculation abbreviation.
2 Release activities are from engineering report's Manufacturing (Mfg), Processing (Proc) and Use release activity labels.
  Multiple release activities are combined in one exposure scenario if their releases occur at same location.
[3] Exposure calculations are Acute Dose Rate (ADR), Lifetime Average Daily Dose (LADD), and Probabilistic Dilution 
  Model (PDM).  There may be one, two, or all three exposure calculations per exposure scenario.
  CC is the aquatic concentration of concern.
[4] This column displays concentration values for the 7Q10 streamflow, which is defined as the average daily streamflow 
   of the seven consecutive days of lowest flow within a ten year period.
Remarks:  
PROC1, 2, 3, 4, 5, 6, 7, 8  -  POTW (Ind.);
USE1, 2, 3, 4  -  Metal Finishing
USE5  -  POTW (All); 
USE6  -  Plastic Resins and Synthetic Fiber Manufacture

                          POST-FOCUS EXPOSURE REPORT
                                       
Chemical ID:  P-12-0433		                                               Reviewer: Tobias/HDJ
                                       
  This updated assessment is based on the Post Focus draft 1 dated 10/13/2016
       
   Results Table: Dose, Concentration, and Days Exceeded Results Summary
   
Exposure Scenario[1]
                                     Water
                                   Landfill
                                   Stack Air
                                 Fugitive Air
Release activity(ies)[2]; exposure calculation(s)[3]
                                Drinking Water
                                Fish Ingestion
                                    7Q10[4]
                                     CC =1
                               PDM Days Exceeded
                                     LADD
                                      ADR
                                 (24-hr conc.)
                                     LADD 
                                (Annual conc.)
                                     ADR 
                                 (24-hr conc.)
                                     LADD 
                                (Annual conc.)

                                      ADR
                                     LADD
                                      ADR
                                     LADD
                                       
                                       
                                       
                                       
                                       
                                       
                                       

                                   mg/kg/day
                                   mg/kg/day
                                   mg/kg/day
                                   mg/kg/day
                                     μg/l
                                    # Days
                                   mg/kg/day
                             mg/kg/day (ug/m[3])
                             mg/kg/day (ug/m[3])
                             mg/kg/day (ug/m[3])
                             mg/kg/day (ug/m[3])
PROC2 (water-based): Max ADR
                                   6.41E-03
                                      ---
                                   2.00E-01
                                      ---
                                   2.90E+02
                                      ---
                                      ---
                                   2.93E-02
                                  (1.60E+02)
                                      ---
                                   1.20E-04
                                  (6.60E-01)
                                      ---
PROC2 (water-based): PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   6.19E+00
                                      41
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC2 (water-based): Max LADD
                                      ---
                                   4.46E-06
                                      ---
                                   3.22E-05
                                      ---
                                      ---
                                   3.42E-05
                                      ---
                                   6.67E-05
                                  (8.60E-01)
                                      ---
                                   6.80E-07
                                  (8.78E-03)
PROC2 (oil-based): Max ADR
                                   1.23E-02
                                      ---
                                   3.80E-01
                                      ---
                                   5.54E+02
                                      ---
                                      ---
                                   6.40E-02
                                  (3.50E+02)
                                      ---
                                   3.50E-04
                                  (1.91E+00)
                                      ---
PROC2 (oil-based): Max LADD
                                      ---
                                   6.54E-06
                                      ---
                                   4.72E-05
                                      ---
                                      ---
                                   5.02E-05
                                      ---
                                   9.76E-05
                                  (1.26E+00)
                                      ---
                                   6.49E-07
                                  (8.38E-03)
PROC3: Max ADR
                                   3.78E-03
                                      ---
                                   1.20E-01
                                      ---
                                   1.71E+02
                                      ---
                                      ---
                                   1.83E-02
                                   (1.0E+02)
                                       
                                   1.20E-04
                                  (6.60E-01)
                                      ---
PROC3: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   3.61E+01
                                      31
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC3: Max LADD
                                      ---
                                   2.63E-06
                                      ---
                                   1.90E-05
                                      ---
                                      ---
                                   2.72E-05
                                      ---
                                   5.29E-05
                                  (6.80E-01)
                                      ---
                                   6.80E-07
                                  (8.78E-03)
PROC4: Max ADR
                                   1.25E-04
                                      ---
                                   3.87E-03
                                      ---
                                   5.67E+00
                                      ---
                                      ---
                                   2.89E-03
                                  (1.58E+01)
                                      ---
                                   1.20E-04
                                  (6.60E+01)
                                      ---
PROC4: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.20E-01
                                       0
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
PROC4: Max LADD
                                      ---
                                   8.75E-08
                                      ---
                                   6.31E-07
                                      ---
                                      ---
                                   1.74E-05
                                      ---
                                   3.38E-05
                                  (4.40E-01)
                                      ---
                                   6.80E-07
                                  (8.78E-03)
USE2 (water-based): Max ADR
                                   4.68E-03
                                      ---
                                   8.52E-02
                                      ---
                                   2.20E+02
                                      ---
                                      ---
                                   6.39E-03
                                  (3.49E+01)
                                      ---
                                      ---
                                      ---
USE2 (water-based): PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   2.20E+02
                                      243
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE2 (water-based): Max LADD
                                      ---
                                   9.09E-05
                                      ---
                                   6.56E-04
                                      ---
                                      ---
                                   1.88E-04
                                      ---
                                   3.65E-04
                                  (4.72E+00)
                                      ---
                                      ---

Exposure Scenario[1]
                                     Water
                                   Landfill
                                   Stack Air
                                 Fugitive Air
Release activity(ies)[2]; exposure calculation(s)[3]
                                Drinking Water
                                Fish Ingestion
                                    7Q10[4]
                                     CC =1
                               PDM Days Exceeded
                                     LADD
                                      ADR
                                 (24-hr conc.)
                                     LADD 
                                (Annual conc.)
                                     ADR 
                                 (24-hr conc.)
                                     LADD 
                                (Annual conc.)

                                      ADR
                                     LADD
                                      ADR
                                     LADD
                                       
                                       
                                       
                                       
                                       
                                       
                                       

                                   mg/kg/day
                                   mg/kg/day
                                   mg/kg/day
                                   mg/kg/day
                                     μg/l
                                    # Days
                                  mg/kg/day 
                             mg/kg/day (ug/m[3])
                             mg/kg/day (ug/m[3])
mg/kg/day (ug/m[3])
                             mg/kg/day (ug/m[3])
USE2 (oil-based): Max ADR
                                   9.69E-04
                                      ---
                                   1.76E-02
                                      ---
                                   4.54E+01
                                      ---
                                      ---
                                   1.54E-02
                                  (8.42E+01)
                                      ---
                                      ---
                                      ---
USE2 (oil-based): PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   4.54E+01
                                      203
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE2 (oil-based): Max LADD
                                      ---
                                   1.88E-05
                                      ---
                                   1.36E-04
                                      ---
                                      ---
                                   4.22E-04
                                      ---
                                   8.21E-04
                                  (1.06E+01)
                                      ---
                                      ---
USE3: Max ADR
                                   2.81E-03
                                      ---
                                   5.11E-02
                                      ---
                                   1.32E+02
                                      ---
                                      ---
                                   3.82E-03
                                  (2.09E+01)
                                      ---
                                      ---
                                      ---
USE3: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   1.32E+02
                                      237
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE3: Max LADD
                                      ---
                                   5.46E-05
                                      ---
                                   3.93E-04
                                      ---
                                      ---
                                   1.13E-04
                                      ---
                                   2.20E-04
                                  (2.84E+00)
                                      ---
                                      ---
USE4: Max ADR
                                   9.45E-05
                                      ---
                                   1.72E-03
                                      ---
                                   4.43E+00
                                      ---
                                      ---
                                   1.28E-04
                                   (7.00E-1)
                                      ---
                                      ---
                                      ---
USE4: PDM1
                                      ---
                                      ---
                                      ---
                                      ---
                                   4.43E+00
                                      66
                                      ---
                                      ---
                                      ---
                                      ---
                                      ---
USE4: Max LADD
                                       
                                   1.83E-06
                                      ---
                                   1.32E-05
                                      ---
                                      ---
                                   3.79E-06
                                      ---
                                   7.38E-06
                                  (9.53E-02)
                                      ---
                                      ---
[1] Exposure scenario titles consist of release activity followed by exposure calculation abbreviation.
2 Release activities are from engineering report's Manufacturing (Mfg), Processing (Proc) and Use release activity labels.
  Multiple release activities are combined in one exposure scenario if their releases occur at same location.
[3] Exposure calculations are Acute Dose Rate (ADR), Lifetime Average Daily Dose (LADD), and Probabilistic Dilution 
  Model (PDM).  There may be one, two, or all three exposure calculations per exposure scenario.
  CC is the aquatic concentration of concern.
[4] This column displays concentration values for the 7Q10 streamflow, which is defined as the average daily streamflow 
   of the seven consecutive days of lowest flow within a ten year period.

 SUPPLEMENTAL INFORMATION

SUPPLEMENTAL DATA FOR APPENDIX E (ChemSteer Engineering Reports):

p120433.ceb  -  23 page pdf file
p120453.ceb - 60 page pdf file

SUPPLEMENTAL DATA FOR APPENDIX F (E-FAST Exposure Reports):

P-12-0433.exp1_Draft Final_REVISED_022013  -  9-page pdf file
P-12-0453.exp1_Draft Final_102512  -  21-page pdf file