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 than the background from atmospheric deposition (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 from the Table:
 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), 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 and LCCPs are somewhat limited and conclusions vary with type of CP product 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 congener groups 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 congener groups in MCCP products 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 (summarized in Appendix C). 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 and LCCPs 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
Overall 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 [14]C 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 AA-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/OPPT 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" (USEPA 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<PHONE_NUMBER>2 (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.

     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 radiolabelled 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 radiolabelled 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 (USEPA, 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 USEPA (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 USEPA (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 (USEPA, 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 USEPA (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 USEPA (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 (Johnson, 2005; cited in: ECB, 2008). Oral studies (Scott, 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