TSCA New Chemicals Program (NCP) 

Chemical Categories in Support of

SNURs for 36 Chemical Substances

EPA Docket: EPA-HQ-OPPT-2010-1075

July 13, 2011
 TSCA NEW CHEMICALS PROGRAM 

 (NCP) 

 CHEMICAL CATEGORIES

Office of Pollution Prevention and Toxics 

U.S. Environmental Protection Agency 

1200 Pennsylvania Ave., NW 

Washington, D.C. 20460 

Contacts: 

 Kenneth Moss (moss.kenneth@epa.gov) 

 Rebecca Jones (jones.rebecca@epa.gov) 

Kelly Mayo-Bean (mayo.kelly@epa.gov) 

Last revised: August, 2010 
ii 

INTRODUCTION 

Disclaimer and Purpose of This Document: 

EPA's Office of Pollution Prevention and Toxics (OPPT) groups chemicals with shared chemical 

and toxicological properties into categories so that PMN reviews are facilitated. PMN submitters 

and EPA reviewers benefit from the accumulated data and past decisions represented by a 

category. EPA considers all PMNs, including new chemical substances which fall within such 

categories, on a case-by-case basis and uses the most appropriate structural analogue to support 

any concerns for health or environmental effects. For any new chemical substance, if EPA 

determines, under TSCA section 5(e), that the substance "may present an unreasonable risk of 

injury to health or the environment,” the PMN substance can be subjected to appropriate control 

actions and/or testing under TSCA section 5(e). This “may present” finding is developed through 

the application of category-based or chemical-by-chemical assessment of hazard endpoints and 

case-specific exposure assessment. 

The categories included in this compilation represent chemicals for which sufficient assessment 

experience has been accumulated so that hazard concerns and testing recommendations vary 

little from chemical to chemical within the category. Thus, these categories do not necessarily 

represent the chemicals of greatest concern to the Agency. By the same token, the categories are 

also not intended to be a comprehensive list of all substances that may be subject to further 

action in the New Chemicals Program. 

If a new chemical substance is structurally similar to a substance for which EPA has positive 

toxicity data and there is sufficient exposure, EPA may regulate that substance under section 5(e) 

of the Toxic Substances Control Act (TSCA) based on its potential unreasonable risk. The 

hazard potential of a PMN substance is dependent on the molecular weight of the compound, the 

presence/absence of activating/deactivating substituents, other physical/chemical properties, and 

the likely route of exposure. Typically, concerns are confined to chemicals with molecular 

weights <1,000 whenever inhalation exposure to humans or environmental release is expected, 

and to species <500 when dermal exposure to humans is expected. 

This document contains references to the "Harmonized Test Guidelines" developed by EPA's 

Office of Prevention, Pesticides and Toxic Substances (renamed the Office of Chemical Safety 

and Pollution Prevention in 2010) for use in the testing of pesticides and toxic substances, and 

the development of test data that must be submitted to the Agency for review under Federal 

regulations. These Harmonized Test Guidelines can be found at 

http://www.epa.gov/ocspp/pubs/frs/home/guidelin.htm. This document also contains references 

to test guidelines developed by the Organization for Economic Cooperation and Development 

(OECD). These OECD test guidelines are available from the OECD Bookshop at 

http://www.oecdbookshop.org or SourceOECD at http://www.sourceoecd.org.

 

Additional information on testing conditions and testing options for specific PMN chemical 

substances that appear to fall within one of these categories is available by contacting the New 

Chemicals Management Branch at 202-564-8469 or the TSCA Hotline at 202-554-1404. This 
iii 

document is intended to serve only as a guide for PMN submitters. PMN submitters are urged to 

have protocols and testing schemes evaluated by the New Chemicals Program prior to 

commencing testing on a PMN substance. However, under no circumstance does such an 

evaluation mean that the new chemical substance is not subject to further review during any 

TSCA section 5 review period for the PMN substance or that additional testing or regulatory 

action may not be recommended. Finally, even if EPA does not make the potential unreasonable 

risk finding for a new chemical substance, the Agency may still recommend the use of 

engineering controls or personal protective equipment to reduce exposures in the workplace if 

the PMN substance is a potential irritant or sensitizer. 

Additional Resources/Tools for the TSCA New Chemicals Program:

The hazard and risk assessment of new industrial chemicals is within the purview of U.S. EPA’s 

Office of Pollution Prevention and Toxics within EPA’s Office of Chemical Safety and Pollution 

Prevention (OCSPP). Under the Toxic Substances Control Act (TSCA), OPPT is charged with 

regulating all phases of the life cycle of industrial chemicals including environmental and human 

health impacts resulting from the manufacturing, processing, use, and disposal of a substance. 

TSCA has no minimum data set requirements for new chemicals entering commerce, and 

therefore, OPPT has developed a suite of predictive approaches that are used to fill data gaps 

where little or no experimental data exists. 

In addition to the use of the New Chemical Category Statements presented in this document to 

assist in chemical management decisions, Structure Activity Relationships (SARs) is a technique 

routinely used under the New Chemicals Program to estimate the toxicity of industrial chemicals 

being reviewed in response to PMN submissions. The predictive approaches are used to support 

OPPT chemical management decisions within the TSCA framework and are also used in the 

analysis of existing chemicals. For more information on the use of these tools to estimate 

physical-chemical properties, environmental fate, ecological and human health hazards, and 

exposures and releases please refer to the web pages listed below: 

• Estimations Programs Interface for Windows Suite – EPI Suite – A suite of models used to 

estimate numerous physical-chemical properties, environmental fate, and partitioning of a 

chemical based on structure. Link for EPI Suite: 

http://www.epa.gov/opptintr/exposure/pubs/episuite.htm

• Ecological Structure Activity Relationships – ECOSAR – A hazard estimation tool that uses 

chemical structure descriptors to estimate the acute and chronic toxicity of a substance to aquatic 

organisms. ECOSAR is available as stand alone product or as part of the EPI Suite package of 

programs. Link for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm

• Human Health Non-Cancer Screening Protocol – In this protocol, analogs are chosen for the 

chemical of interest along with associated health effects data to perform read-across activities to 

predict human health effects in the absence of sufficient measured data. An outline of this 

protocol can be reviewed at: http://www.epa.gov/oppt/sf/pubs/noncan-screen.htm. Additionally, 

to assist users in this task, EPA has recently created a new tool to assist in the selection of analogs 

and to help identify publicly available experimental data for chemicals of interest called the 
iv 

Analog Identification Methodology which can be accessed at http://aim.epa.gov

• The Cancer Expert System – OncoLogic – A cancer hazard expert system software package 

which relies on the known carcinogenic effects of chemicals to predict cancer hazard of new 

substances based on structural similarity. The software estimates carcinogenic potential of a 

substance by initiating expert rules for determining cancer potential created from many sources of 

publicly available carcinogenicity data. OncoLogic is capable of estimating carcinogenic 

potential for organics, polymers, fibers, and metals. Link for OncoLogic: 

http://www.epa.gov/oppt/newchems/tools/oncologic.htm

• Chemical Screening Tool for Exposures and Environmental Releases – ChemSTEER – A 

modeling program to estimate occupational exposures and environmental releases of a chemical 

through manufacture, processing and use. This software uses EPA validated models to predict 

environmental releases and worker exposure to a chemical from manufacturing, processing, and 

use. Link for ChemSTEER: http://www.epa.gov/opptintr/exposure/pubs/chemsteerdl.htm

• Exposure and Fate Assessment Screening Tool – E-FAST – A windows based package that 

incorporates several screening level exposure models. E-FAST provides screening level 

estimations of environmental concentration and human exposure due to releases of a chemical to 

the environment. Link for E-FAST: http://www.epa.gov/opptintr/exposure/pubs/efast.htm

EPA offers training in the use and interpretation of these models through workshops under the 

Sustainable Futures Initiative. The goal of the Sustainable Futures training workshops is to 

assist the public in learning more about the application and interpretation of OCSPP’s predictive 

methods, to build on the chemical expertise developed by EPA through chemical regulation 

activities, and to promote the technology transfer of EPA expertise to other chemical 

stakeholders. To learn more about the program and workshops please visit the Sustainable 

Futures website at: http://www.epa.gov/oppt/sf/. 

Changes Made to this August 2010 Revision: 

• The introductory section was revised to include a section entitled “Additional 

Resources/Tools for the TSCA New Chemicals Program” and this section of the 

Introduction was added to identify changes made in this August 2010 version of the 

document. 

• The previous 2002 version of this document contained references to EPA Office of 

Pollution Prevention and Toxics (OPPT) test guidelines that originally appeared in title 

40, chapter I, subchapter R of the Code of Federal Regulations (CFR). Since that time, 

the "Harmonized Test Guidelines" have been developed by EPA's Office of Prevention, 

Pesticides and Toxic Substances (renamed the Office of Chemical Safety and Pollution 

Prevention in 2010) for use in the testing of pesticides and toxic substances, and the 

development of test data that must be submitted to the Agency for review under Federal 

regulations. These Harmonized Test Guidelines can be found at 

http://www.epa.gov/ocspp/pubs/frs/home/guidelin.htm. This current version of the 

Chemical Categories report now contains references to the Harmonized Test Guidelines 

rather than the OPPT test guidelines. For example, the fish acute toxicity test at 40 CFR 

797.1400 has been replaced by Harmonized Test Guideline 850.1075, and the Ready 
v 

Biodegradability test at 40 CFR 796.3180, etc. has been replaced by Harmonized Test 

Guideline 835.3110.

• OPPT has made minor revisions to the following categories to reflect updated 

structure-activity relationships (SARs) for certain classes which are available in version 

1.0 of ECOSAR. In addition to SARs for classes represented in this category document, 

ECOSAR contains many other classes for which SARs are available. For access to 

these SARs and the underlying chemical training sets, please access the class-specific 

documents available in the help menu of the ECOSAR 1.0 model which is available for 

download at: (http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm). 

o Aldehydes 

o Anilines 

o Azides 

o Diazoniums 

o Epoxides 

o Imides 

o Phenols 

o Phosphinate Esters 

o Polynitroaromatics 

o Thiols 

o Substituted Triazines 

• One additional chemical category has been added to the document: Nitriles, allylic and 

vinyl. 

• For those categoies for which biodegradation and/or photolysis testing are identified, the 

recommended guidelines have been changed to reference certain OECD test guidelines. 
vi 

 Table of Contents 

Acid Chlorides .................................................................................................................................1 

Acid Dyes and Amphoteric Dyes ....................................................................................................2 

Acrylamides .....................................................................................................................................5 

Acrylates/Methacrylates ..................................................................................................................8 

Aldehydes ......................................................................................................................................10 

Aliphatic Amines ...........................................................................................................................13 

Alkoxysilanes.................................................................................................................................15 

Aluminum Compounds..................................................................................................................17 

Aminobenzothiazole Azo Dyes .....................................................................................................23 

Anhydrides, Carboxylic Acid ........................................................................................................25 

Anilines..........................................................................................................................................26 

Dianilines .......................................................................................................................................30 

Anionic Surfactants........................................................................................................................34 

Azides ............................................................................................................................................36 

Benzotriazoles................................................................................................................................39 

Benzotriazole-hindered phenols ....................................................................................................42 

Boron Compounds .........................................................................................................................45 

Cationic Dyes.................................................................................................................................50 

Cationic (quaternary ammonium) surfactants................................................................................51 

Cobalt.............................................................................................................................................52 

Diazoniums ....................................................................................................................................56 
vii 

Dichlorobenzidine-based Pigments ...............................................................................................60 

Dithiocarbamates ...........................................................................................................................62 

Epoxides.........................................................................................................................................64 

Esters..............................................................................................................................................65 

Ethylene Glycol Ethers ..................................................................................................................68 

Hydrazines and Related Compounds.............................................................................................70

Hindered Amines ...........................................................................................................................73 

Imides.............................................................................................................................................74 

Diisocyanates .................................................................................................................................77 

β-Naphthylamines, Sulfonated.......................................................................................................80 

Lanthanides or Rare Earth Metals .................................................................................................82 

Neutral Organics ............................................................................................................................86 

Nickel Compounds.........................................................................................................................88 

Nitriles, allylic/vinyl ......................................................................................................................90 

Nonionic Surfactants......................................................................................................................94 

Organotins......................................................................................................................................96 

Peroxides......................................................................................................................................100 

Persistent, Bioaccumulative, and Toxic (PBT) Chemicals..........................................................102 

Phenolphthaleins..........................................................................................................................105 

Phenols.........................................................................................................................................107 

Phosphates, Inorganic ..................................................................................................................110 

Phosphinate Esters .......................................................................................................................113 

Polyanionic Polymers (& Monomers) .........................................................................................116 
viii 

Polycationic Polymers .................................................................................................................117 

Polynitroaromatics .......................................................................................................................118 

Respirable, Poorly Soluble Particulates.......................................................................................121 

Rosin ............................................................................................................................................126 

Stilbene, derivatives of 4,4-bis(triazin-2-ylamino)- ....................................................................128 

Thiols ...........................................................................................................................................131 

Substituted Triazines....................................................................................................................134 

Triarylmethane Pigments/Dyes with Non-solubilizing Groups...................................................135 

Vinyl Esters..................................................................................................................................140 

Vinyl Sulfones .............................................................................................................................142 

Soluble complexes of Zinc...........................................................................................................146 

Zirconium Compounds ................................................................................................................147 
1 

Category: Acid Chlorides Environmental Toxicity 

Definition. This category includes carbonyl chlorides (R-C[=O]Cl) and sulfochlorides 

(R-S[=O]Cl) where R may be either aliphatic or aromatic. Toxicity is limited by the fact that 

this class of compounds hydrolyzes and also, probably, if the octanol/water partition coefficient 

(Kow) is above a log Kow value of 8. It has been assumed that these compounds need to be 

absorbed to be toxic; therefore, compounds with MWs > 1000 will probably be excluded in the 

future once this assumption is confirmed with toxicity information. However, toxicity 

information is needed to confirm this assumption. 

Hazard Concerns. Acute toxicity for three members of this category are available and all have 

been shown to be moderately toxic to aquatic organisms (i.e., acute toxicity values between 1 

and 100 mg/L): benzoyl chloride, fish 96-h LC50 = 35.0 mg/L, an aromatic dicarboxyl 

dichloride, fish 96-h LC50 = 6.2 mg/L, and benzene sulfochloride, fish 48-h LC50 = 3.0 mg/L. 

All of these tests have been done with the static method using nominal concentrations. It is 

unclear just how acid chlorides are toxic to aquatic organisms. It is known that acid chlorides 

hydrolyze to the carboxylic/sulfonic acid and HCl. It is not known if the toxic effect is the result 

of (1) absorption of the acid chloride and hydrolysis within the membrane, or (2) the HCl 

produced from the hydrolysis. It is known that the carboxylic/sulfonic-acid hydrolysis products 

are of low toxicity. 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW when enough information is obtained. In general, when the log Kow value is < 8, 

the environmental base set of tests will be requested for aquatic releases and the terrestrial base 

set of tests will be recommended for terrestrial exposures. When the log Kow is > 8, testing will 

be requested until enough information is obtained to determine whether these compounds will 

have no toxic effects at saturation. Generally, members of this category will have MWs of less 

than 1000, but testing of members with a MW > 1000 may be requested to confirm whether acid 

chlorides have to be absorbed to be toxic. 

General Testing Strategy. The testing strategy for acid chlorides will consist of two steps. 

(1) Hydrolysis (Harmonized Test Guideline 835.2120) will be recommended. Depending on 

the outcome of this environmental fate testing and reassessment, (2) the aquatic base set of 

environmental toxicity tests will be recommended for aquatic exposures with the fish acute 

toxicity test done once or twice. 

Chronic toxicity testing for aquatic organisms include: the fish early life state toxicity test, the 

daphnid partial life cycle toxicity test and the algal toxicity test. 

The terrestrial base set of environmental toxicity tests (i.e., the early seeding growth test, the 

earthworm acute toxicity test and the soil microbial community bioassay) will be recommended 

for terrestrial exposures. Chronic toxicity testing for terrestrial organisms include: the plant 

whole life cycle test, the plant uptake test, and the soil microbial community bioassay. 

October, 1990 
2 

Category: Acid Dyes and Amphoteric Dyes Environmental Toxicity 

Definition. Organic dyes are divided into four classes depending on the type of electronic 

charge of the dye: nonionic (neutral dyes); anionic (negative charge or acid dyes); cationic 

(positive charge) dyes; and amphoteric (mixture of positive and negative charges on same 

molecule) dyes. Nonionic or neutral dyes are assessed as neutral organic chemicals for which 

there is a separate category description, and cationic dyes also have a separate category 

description. Amphoteric dyes are assessed either as cationic or anionic dyes depending on 

dominant net charge. 

Hazard Concerns. Analysis of over 200 acid dyes (Auer et al. 1990, Nabholz 1990, Sigman et 

al. 1983, Tonogai et al. 1979, Little and Lamb 1972, ADMI 1974) have indicated that some 

monoacid and diacid dyes can show moderate to high toxicity (i.e., acute values < 100 mg/L and 

< 1 mg/L) to fish and aquatic organisms. Dyes with three or more acid groups showed low 

toxicity (i.e., acute values > 100 mg/L) towards fish and invertebrates. Some metal chelated 

dyes, i.e., Al, Co, Cr, Fe, have shown moderate toxicity towards fish and daphnids and the 

toxicity has not been explained by the residual free (un-chelated) metal ion in the dye product. 

All acid dyes showed moderate toxicity towards green algae. Analysis of available data (Auer 

et al. 1990, Nabholz 1990) has suggested that effects to algae were not the result of direct 

toxicity but represented an indirect effect due to shading. Senior regulatory decision-makers in 

OPPT (then OTS) decided in 1988 that the risk to algae from indirect (shading) toxicity was not 

an unreasonable risk for two main reasons: (1) algae grew quickly as soon as the dye was diluted, 

and (2) the release of colored effluents in the U. S. generally results in immediate complaints by 

citizens to their local authorities, e.g., county and state governments. The rapid response by the 

public generally results in quick regulatory action by local officials. 

Since there is no SAR for acid dyes (Auer et al. 1990), hazard profiles for monoacid dyes 

are developed using measured data or data for the nearest analog(s). 

Boundaries. Acids dyes must have some water solubility and molecular weights generally 

need to be near or below 1000. 

General Testing Strategy.

I. Release to Aquatic Ecosystems: 

Tier 1. Because of the above boundary conditions, and the need to assess human 

exposure as well as environmental toxicity, if there is insufficient knowledge about the water 

solubility of the dye, then it should be measured (Harmonized Test Guideline 830.7860). The 

fish and daphnid acute toxicity tests from the aquatic base set of environmental toxicity tests will 

be recommended for aquatic exposures. The acute toxicity tests for fish (Harmonized Test 

Guideline 850.1075) and daphnids (Harmonized Test Guideline 850.1010) will be done using the 

flow-through method with measured concentrations, and effective concentrations will be based 

on 100% active ingredients (AI) and mean measured concentrations. 
3 

If there is no significant risk from the PMN after the results of the fish and daphnid acute 

toxicity tests have been integrated into the risk assessment, then no further testing is 

recommended. However, if there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water—Indirect Photolysis Screening Test 

(Harmonized Test Guideline 835.5270) If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, go to Tier 

4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then 

prepare a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. 

Tier 4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; and statistical analysis of effective concentrations at days 7, 14, 21, and 28. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% active 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, and 21. 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

II. Release to Terrestrial Ecosystems: 

The terrestrial base set of environmental toxicity tests (i.e., the early seedling growth test 

[Harmonized Test Guideline 850.4230], the earthworm toxicity test [Harmonized Test Guideline 

850.6200] and the soil microbial community bioassay [Harmonized Test Guideline 850.5100]) 

will be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial organisms 

include: the plant whole life cycle test (Harmonized Test Guideline 850.4150), the plant uptake 

test (Harmonized Test Guideline 850.4800), and the soil microbial community bioassay 

(Harmonized Test Guideline 850.5100). 
4 

References.

American Dye Manufacturers Institute, Inc. (ADMI), 1974, "Dyes and the Environment: 

Reports on Selected Dyes and Their Effects," Vol. II, ADMI, New York. 

Auer, C.M., Nabholz, J.V. and Baetcke, K.P., 1990, "Mode of Action and the Assessment of 

Chemical Hazards in the Presence of Limited Data: Use of Structure-Activity 

Relationships (SAR) under TSCA, Section 5," Environmental Health Perspectives, Vol. 

87, pp. 183-197. 

Little, L.W. and Lamb J.C., III, 1972, "Acute Toxicity of 46 Selected Dyes to the Fathead 

Minnow, Pimephales promelas,"Final Report to the American Dye Manufacturers 

Institute,Inc., UNC Wastewater Research Center, Department of Environmental Sciences 

and Engineering, School of Public Health, University of North Carolina, Chapel Hill, 

NC. 

Nabholz, J.V., 1990, "The OTS PMN ECOTOX Data Base: a Confidential Business Information 

(CBI) Collection of Environmental Toxicity Data from New Chemical Submissions 

Under Sec. 5," Unpublished, Environmental EffectsBranch, Health and Environmental 

Review Division (TS-796), U. S. Environmental Protection Agency, Washington, DC. 

Sigman, C.C., Helms, C.T., Papa, P.A., Atkinson, D.L., Doeltz, M.K. and Winship-Ball, A., Jan. 

1983, "Anthraquinone Dyes and Related Chemicals: Review and Assessment of Potential 

Environmental and Health Aspects," Final Report to the Dyes Environmental and 

Toxicology Organization, Inc., SRI International, Menlo Park, CA. 

Tonogai, Y., Ito, Y., Iwaida, M., Tati, M., Ose, Y. and Sato, T., 1979, "Studies on the Toxicity of 

Coal-Tar Dyes. II. Examination of the Biological Reaction of Coal-Tar Dyes to Vital 

Body," The Journal of Toxicological Sciences, Vol. 4, pp. 211-219. 

July, 1991; revised June, 1994; revised June 2010 
5 

Category: Acrylamides Human Health and Environmental Toxicity 

Definition. Any new chemical with the following structure is considered to be a member of the 

category: 

A typical acrylamide in the new chemical program is used as a monomer and has a 

molecular weight of <500. The acrylamides of greatest concern are those with a labile 

substituent, e.g., methylol acrylamides, that may release acrylamide per se under metabolic 

conditions. For toxicity to aquatic organisms, there is a concern for all substituted acrylamides 

with molecular weights of <1000 and log Kow of <8.0. 

Hazard Concerns. Based on analogy to acrylamide per se, members of the class are 

considered potential carcinogens, heritable mutagens, reproductive and developmental toxicants, 

and toxic to aquatic organisms. Acrylamides are also potential neurotoxins based on data for a 

number of low molecular weight acrylamides. 

Boundaries. Structures with an acrylamide equivalent weight of >5,000 are presumed not to 

pose a hazard under any conditions. Typically, concerns are confined to those species with 

molecular weights <1,000 whenever inhalation (or environmental) exposure is expected, and to 

species <500 when dermal, but not inhalation, exposure to humans is expected. 

Occupational Exposure Controls. Because acrylamides are expected to be absorbed via the 

dermal route, glove permeation testing conducted in accordance with standard ASTM testing 

protocols may be required, depending upon estimated workplace exposures and the hazard 

identified for the particular acrylamide submitted as a PMN. 
6 

General Testing Strategy.

Tier 1. To properly assess human and environmental toxicity or exposure, certain 

physical-chemical or environmental fate properties need to be measured: 

- Water solubility (Harmonized Test Guideline 830.7860) 

- Kow (Harmonized Test Guideline 830.7570 or 830.7550; or OECD 123, Partition 

Coefficient (1-Octanol/Water): Slow-Stirring Method) 

- Vapor pressure (Harmonized Test Guideline 830.7950) 

- Melting point-melting range (Harmonized Test Guideline 830.7200) 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

The physical state and electronic charge of the PMN substance should also be reported. 

Tier 2. EPA considers the following tests to be the most appropriate for acrylamides found to 

pose an unreasonable risk to human health: 

- 90-day subchronic toxicity (Harmonized Test Guideline 870.3100) with functional 

observational battery and neuropathology (Harmonized Test Guideline 870.6200). 

- A rodent dominant lethal assay (Harmonized Test Guideline 870.5450). If positive, a 

rodent heritable translocation test (Harmonized Test Guideline 870.5460) would be the 

appropriate followup test. 

- A 2-year carcinogenicity test (Harmonized Test Guideline 870.4200) in rats and mice. 

To address environmental toxicity concerns, the following testing is recommended, for 

acrylamides with log Kow <5: acute aquatic toxicity testing in algae, daphnid, and fish. The 

acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids (Harmonized 

Test Guideline 850.1010) will be done using the flow-through method with measured 

concentrations; effective concentrations will be based on 100% active ingredients (AI) and mean 

measured concentrations; measured TOC of dilution water in the control <2 mg TOC/L; the 

highest treatment concentration on a mean measured-basis should equal the aqueous solubility 

limit; and solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but 

cannot be used to artificially enhance the water solubility of the PMN beyond its aqueous 

solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 

static methods; measured concentrations; effective concentrations based on 100% active 
7 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; and the highest treatment concentration on a mean measured-basis equal to the 

aqueous solubility limit. Solvent can be used to assist the PMN substance to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the 

PMN substance beyond its aqueous solubility limit. 

For acrylamides with log Kow >5 and <8, aquatic toxicity testing should be for chronic 

effects only: (1) fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing with 

rainbow trout (Harmonized Test Guideline 850.1400), with flow-through methods; measured 

concentrations; effective concentrations based on 100% active ingredients (AI) and mean 

measured concentrations; and statistical analysis of effective concentrations at days 30, 45, 60, 

75, and 90; (2) daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% active 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, and 21; and (3) algal toxicity testing (Harmonized Test Guideline 

850.5400), with static methods; measured concentrations; effective concentrations based on 

100% active ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; and the highest treatment concentration on a mean measured-basis equal to the 

aqueous solubility limit. Solvent can be used to assist the PMN substance to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the 

PMN substance beyond its aqueous solubility limit. 

November 1990; revised July 1993; revised October 1995; revised June 2010 
8 

Category: Acrylates/Methacrylates Environmental Toxicity 

(Human Health, case-by-case) 

Definition. Any molecular structure containing one or more of the following reactive groups is 

considered to be a member of the class: 

 O 

 ║

- acrylate, CH2=CH-C-O- 

 O 

 ║

 - methacrylate, CH2=C-C-O- 

 | 

 CH3

Hazard Concerns. 

Human Health: As a result of testing conducted under an agreement between the Agency and 

the Specialty Acrylates and Methacrylates (SAM) Panel of the Chemical Manufacturers 

Association (CMA), EPA no longer controls new chemical acrylates or methacrylates as a 

category based on health concerns. However, if a new acrylate is structurally similar to a 

substance for which EPA has positive toxicity data, EPA may regulate that substance under 

TSCA section 5(e) based on its potential unreasonable risk. This will be done on a 

case-by-case basis and is expected to effectively eliminate most regulation of acrylates, 

especially higher molecular weight and polymeric substances. Despite the fact that EPA no 

longer expects to make a potential unreasonable risk to human health finding for many of the 

new acrylates, EPA still recommends the use of engineering controls or personal protective 

equipment to reduce exposures in the workplace in recognition of their potential as irritants and 

sensitizers. 

Environmental Toxicity: The ecotoxicity of acrylates and methacrylates is a function of the 

octanol-water partition coefficient (log P or log Kow). They exhibit simple narcosis at log Kow 

values >5, but display excess toxicity at lower log Kow values. The toxicity of acrylates and 

methacrylates can be predicted by a QSAR (quantitative structure-activity relationship), although 

there are some members of the class such as allyl methacrylate that are significantly more toxic 

than predicted by the QSAR. 

Boundaries. Typically, environmental toxicity concerns are confined to those chemicals with 

molecular weights <1,000. Acute and chronic toxicity is possible for chemicals with log Kow 

values <5, and chronic toxicity is possible for chemicals with log Kow values <8. 
9 

General Testing Strategy

Tier 1. To properly assess environmental toxicity or exposure, certain physical-chemical or 

environmental fate properties need to be measured: 

- Water solubility (Harmonized Test Guideline 830.7860) 

- Kow (Harmonized Test Guideline 830.7550, 830.7560, or 830.7570; or OECD 123, 

Partition Coefficient (1-Octanol/Water): Slow-Stirring Method) 

- Vapor pressure (Harmonized Test Guideline 830.7950) 

- Melting point-melting range (Harmonized Test Guideline 830.7200) 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

The physical state and electronic charge of the PMN substance should also be reported. 

Tier 2. To address environmental toxicity concerns, the following testing is recommended: 

acute aquatic toxicity testing in algae (Harmonized Test Guideline 850.5400), daphnid 

(Harmonized Test Guideline 850.1010), and fish (Harmonized Test Guideline 850.1075) (all 

tests using measured concentrations; algae: static method, daphnid and fish: flow-through 

method). 

September, 1988; revised July, 1993; revised January, 1997; revised June 2010. 
10 

Category: Aldehydes Environmental Toxicity 

Definition. Aldehydes are a class of organic compounds characterized by the functional group 

R-C(=O)-H. Aldehydes are ionizable in water and exhibit excess aquatic toxicity in addition to 

narcosis. Polyaldehydes are more toxic than monoaldehydes to aquatic organisms and 

acrylic/vinyl/allylic aldehydes, e.g., acrolein, are more toxic than polyaldehydes. 

Vinyl/allylic/acrylic aldehydes are a class of organic compounds characterized by both the 

aldehyde, R-C(=O)-H, and vinyl, H2C=C-R, or allylic, R-C=C-R, functional groups. Allylic 

and vinyl aldehydes, e.g., acrolein, C=CC(=O), exhibit excess toxicity. 

Hazard Concerns: It is assumed that aldehydes need to be absorbed to be toxic, therefore, 

aldehydes with MW >1000 will be excluded from this category. Acute toxicity for aldehydes is 

known to be limited by the octanol/water partition coefficient (Kow). Above a log Kow value of 

>6.0, aldehydes show no effects at saturation for acute effects during 96-h exposures to fish. 

Aldehydes which are solids at room temperature may show no toxicity at saturation at lower Kow

values depending on the melting point, i.e., the higher the melting point at a given Kow, the 

greater the likelihood that no toxicity will be observed at saturation. For solids, the no effects 

at saturation has to be determined on a case-by-case basis. There are no measured upper Kow

limits for chronic toxicity at this time, but it may not be much above a log Kow = 8. Future 

testing will determine Kow limits. The aquatic toxicity for aldehydes may be determined through 

SAR analysis by EPA using ECOSAR – a hazard estimation tool that uses chemical structure 

descriptors to estimate the acute and chronic toxicity of a substance to aquatic organisms. [Link 

for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm] 

Environmental Fate: 

Boundaries: MW <1000. Log Kow <6.0 for acute toxicity to fish and aquatic invertebrates; 

log Kow <6.4 for toxicity to green algae as a 96-h EC50; and log Kow assumed to be <8.0 for 

chronic toxicity to aquatic organisms, but could be higher. 

General Testing Strategy: 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for 

aquatic exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and 

daphnids (Harmonized Test Guideline 850.1010) will be done using the flow-through method 

with measured concentrations; effective concentrations will be based on 100% active 

ingredients (AI) and mean measured concentrations; measured TOC of dilution water in the 

control; ideally, mean measured concentrations in the highest treatment concentration should be 

equal the aqueous solubility limit; and solvent can be used to assist the aldehyde to reach its 

aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility of 
11 

the aldehyde beyond its aqueous solubility limit. Stock solutions in water should be adjusted to 

pH near 7.0. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 

static methods; measured concentrations; effective concentrations based on 100% active 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; ideally, mean measured concentrations in the highest treatment concentration 

should be equal the aqueous solubility limit; and solvent can be used to assist the aldehyde to 

reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the water 

solubility of the aldehyde beyond its aqueous solubility limit. Stock solutions in water should 

be adjusted to pH near 7.0. 

If there is no significant risk from the aldehyde after the results of the environmental base 

set have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the aldehyde after the results of biodegradation testing have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured 

TOC of dilution water in the control; ideally, mean measured concentrations in the highest 

treatment concentration should be equal the aqueous solubility limit; solvent can be used to 

assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially 

enhance the water solubility of the PMN beyond its aqueous solubility limit; and the 7-d ELS 

stage toxicity test cannot be substituted for the 28-d ELS toxicity test because the 7-d ELS 

toxicity test may underestimate chronic toxicity measured by the 28-d ELS toxicity test when the 

Chronic Values are compared. Stock solutions in water should be adjusted to pH near 7.0. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% 

active ingredients (AI) and mean measured concentrations; statistical analysis of effective 
12 

concentrations at days 7, 14, and 21; measured TOC of dilution water in the control; ideally, 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; solvent can be used to assist the PMN to reach its aqueous solubility 

limit quicker, but cannot be used to artificially enhance the water solubility of the PMN beyond 

its aqueous solubility limit; and the 7-d daphnid chronic toxicity test cannot be substituted for the 

21-d toxicity test because the fish 7-d ELS toxicity test may underestimate chronic toxicity 

measured by the fish 28-d ELS toxicity test when the chronic values are compared. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental 

toxicity tests (i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the 

earthworm toxicity test [Harmonized Test Guideline 850.6200] and the soil microbial 

community bioassay [Harmonized Test Guideline 850.5100]) will be recommended for 

terrestrial exposures. Chronic toxicity testing for terrestrial organisms include: the plant whole 

life cycle test (Harmonized Test Guideline 850.4150), the plant uptake test (Harmonized Test 

Guideline 850.4800), and the soil microbial community bioassay (Harmonized Test Guideline 

850.5100). 

July, 1996; revised June 2010
13 

Category: Aliphatic Amines Environmental Toxicity 

Definition. This category includes primary amines, secondary amines and tertiary amines; or 

monoalkyl amines, dialkly amines and trialkyl amines, respectively. This group includes 

alkanes, alkenes and alkynes; substitutions on carbon (alkyl) chains may include but not be 

limited to halogens and hydroxyls; insertions in alkyl chain may include but not be limited to 

ethoxys, propoxys, ethers, sulfides, disulfides and polysulfides; amine oxides are also included in 

this category; fatty polyamines (e.g., diamines, triamines, tetraamines, pentamines, etc) are 

also included; amines may either be un-ionized (free) or ionized; and strong ion pairs may also 

be included. 

Hazard Concerns: Members of this category can be highly toxic to all groups of freshwater 

organisms (i.e., fish, aquatic invertebrates and green algae). Toxicity is related to the length of 

the hydrophobic carbon chains: the longer (or greater the number of carbons) the chain the more 

toxic to aquatic organisms when the number of amines is constant; and the greater the number of 

amines, the greater the toxicity given a constant carbon chain length. Small aliphatic amines 

are more toxic to algae than fish and invertebrates; higher molecular weight amines are equally 

toxic to all aquatic organisms. Small aliphatic amines which are un-ionized are more toxic to 

fish than when they are ionized; toxicity to algae appears to be unaffected by ionization. Strong 

ion pairs are generally much less toxic to fish and invertebrates because of solubility limitations, 

but remain highly toxic to green algae. The toxicity of each amine will be predicted using 

structure-activity relationships (SARs) and analogs contained in a generic standard 

environmental hazard review for aliphatic amines. 

Boundaries: There are no lower boundaries and the upper boundary is unknown at this time. 

It is known that a C13-NH3 Cl is still toxic to fish at less than 1 mg/L. An upper boundary for 

carbon chain length will probably be about 20 carbons but more information is needed at this 

time. Generally, members of this category will have molecular weights less than 1000. 
14 

General Testing Strategy

Tier 1. The base set of environmental toxicity tests in clean dilution water and two fish 

acute toxicity tests done in the presence of humic acid (i.e., TOC) will be recommended. These 

tests will be done under static methods with nominal concentrations. Smaller amines (e.g., 

Schiff bases) are expected to demonstrate less mitigation by humic acid (larger log Kow , greater 

mitigation; increase log Kow correlates to increased MW). If hydrolysis 1/2 life is less than 

one hour, test the hydrolysis product; if it is greater than one hour, test parent material. 

Tier 2. If TOC significantly reduces the toxicity to water column species, then toxicity 

testing for toxicity to benthic organisms (i.e., organisms that ingest sediment) will be 

recommended; however, if TOC does not significantly reduce the toxicity to water column 

species, then chronic toxicity with fish and aquatic invertebrates will be recommended as well as 

aerobic biodegradation testing. 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

September 1988; revised November 1995; revised June 2010
15 

Category: Alkoxysilanes Human Health 

Environmental Toxicity 

Definition. Any molecular structure containing one or more of the following reactive groups is 

considered to be a member of the category. 

 | | 

 -C-O-Si- 

 | | 

The "typical" new chemical of concern is a polymer with a substantial fraction of species with 

molecular weights <1000 and pendant trimethoxy- or triethoxysilane groups. 

Hazard Concerns.

Health - Concern for lung toxicity from inhalation of vapors or aerosols is based on data 

for a number of low-molecular-weight alkoxysilanes. Trimethoxysilane (TMS) is clearly the 

most toxic member of the class causing irreversible lung effects at low doses, but the Agency 

does not consider it appropriate to use TMS as a regulatory benchmark for all alkoxysilanes. 

For trimethoxysilane monomers and polymers with a low trimethoxysilyl equivalent 

weight, a NOAEL of 10 ppm (about 11 mg/kg/day) based on a 90-day study with 

vinyltrimethoxysilane in monkeys is deemed an appropriate generic benchmark. 

Alkoxysilanes in which the alkyl substituent is not a methyl group do not appear to be as 

toxic as methoxysilanes. The New Chemicals Program currently uses a generic benchmark 

NOAEL of 75 mg/kg/day, based on a 90-day inhalation study with tri(isopropenoxy)silane, for 

alkoxysilanes other than methoxysilanes. 

Ecotoxicity - Alkoxysilanes are highly toxic to algae and moderately toxic to aquatic 

invertebrates. For example, the daphnid 48-hr LC50 for dimethyldiethoxysilane is 1.25 mg/L, 

and the 15-day algal EC95's for vinyltriethoxysilane, tetraethoxy-silane, and 

trifluoropropenyl(methyl)diethoxysilane are all approximately 10 μg/L. 

Boundaries. Methoxy- and ethoxysilanes are presumed not to pose a hazard under any 

conditions if the equivalent weight is > 5,000 and no more than 25% of species have molecular 

weights less than 1,000 and no more than 10% of species have molecular weights less than 500. 

For alkoxysilanes with alkyl substituents larger than propyl groups, the equivalent weight cutoff 

is 1,000. The degree of concern depends on the relative abundance of lower molecular weight 

species, but there is no molecular weight threshold above which there would be no concern. 

To better define the boundaries of the category, EPA seeks testing on a limited number of 

alkoxysilanes that focuses on (1) the relationship between molecular weight (or alkoxysilyl 
16 

equivalent weight) and inhalation toxicity and (2) the importance of increasing alkoxy chain 

length in limiting toxicity. 

General Testing Strategy 

 

The Agency recommends the following testing as appropriate to address health and 

environmental toxicity concerns for this category: 

1. 90-day subchronic test in rodents by the inhalation route (Harmonized Test Guideline 

870.3100). 

2. Hydrolysis (Harmonized Test Guideline 835.2120) . If t1/2 is less than one hour, base 

set ecotoxicity testing (see "3," below) is conducted with the hydrolysis products only. If t1/2 is 

greater than one hour, base set ecotoxicity testing is conducted with the parent material; the 

PMN submitter has the option of also testing with the hydrolysis products. 

3. Base-set ecotoxicity testing to include fish (Harmonized Test Guideline 850.1075) using 

the static method, daphnids (Harmonized Test Guideline 850.1010) using the static method and 

algae (Harmonized Test Guideline 850.5400) using the static method, all nominal concentrations. 

 Direct dilution of the test alkoxysilane and organisms is added within 10 minutes. The 

static-renewal method is used for fish and daphnid test, plus an additional fish test using aged 

stock solution. 

Results of the acute ecotoxicity testing may trigger chronic fish (Harmonized Test 

Guideline 850.1400) and daphnid (Harmonized Test Guideline 850.1300) testing. 

4. Physical-chemical or environmental fate testing including, as appropriate: 

- Melting point (Harmonized Test Guideline 830.7200) or boiling point (Harmonized 

Test Guideline 830.7220) 

- Water solubility (Harmonized Test Guideline 830.7840 or 830.7860) 

- Log Kow (Harmonized Test Guideline 830.7550, 830.7560 or 830.7570; or OECD 123, 

Partition Coefficient (1-Octanol/Water): Slow-Stirring Method ) 

- Vapor pressure (Harmonized Test Guideline 830.7950) 

- Phototransformation of Chemicals in Water—Direct Photolysis (OECD 316) or Indirect 

Photolysis Screening Test (Harmonized Test Guideline 835.5270). 

Need for water solubility, log Kow, and photolysis testing determined by outcome of 

above hydrolysis testing. 

September, 1988; revised June, 1994 
17 

Category: Aluminum Compounds

Risk Management Statement. Greatest concern is for soluble forms of aluminum (Al). If 

water solubility is greater than 1 part per billion (1 ppb), the Agency will prohibit releases of the 

PMN substance to water pending the submission of environmental toxicity testing. 

Definition. This category includes inorganic salts of Al, complexes between Al and organic 

acids or chelates of Al by polyanionic monomers, and organoAl compounds, i.e., Al 

covalently-bonded with carbon. For example, some inorganic Al salts include: Al hydroxide, 

Al chloride, Al fluoride, Al nitrate, Al phosphate, and Al sulfate. Not included in this category 

are dyes complexed with Al (see dye categories addressed elsewhere within this ATSCA New 

Chemicals Program Chemical Categories@ document). 

Hazard Concerns. Soluble salts of Al are known to be highly toxic to green algae and 

moderately toxic to fish and aquatic invertebrates at pH values between 6.5 to 9.0 and in terms of 

soluble Al in mg Al/L. Toxicity information is available for Al chloride, Al sulfate, and Na 

aluminate. The Office of Water (USEPA, 1988, EPA440/5-86-008) cited Seipt et al. (1984, 

Water Air Soil Pollut. 23:81-95) who concluded that "the simple hydroxides (Al(OH)2+ and 

Al(OH)2

+

) are regarded as the most dangerous forms while organically bound Al and polymeric 

forms are less toxic or essentially harmless." The Office of Water (USEPA, 1988) also 

concluded that solutions of Al in water approach chemical equilibrium rather slowly and that Al 

can form strong complexes with fulvic and humic acids. 

The toxicity profile for soluble Al salts, listed below, is based on (1) available measured (M) 

toxicity data, (2) mg Al/L (ppm Al), (3) pH between 6.5 and 9.0, and (4) moderate hardness 

(about 150.0 mg/L as CaCO3). 

fish (FHM) 96-h LC50 = 35.0 M, pH 7.3, H220 

fish (RT) 96-h LC50 = 8.6 M, pH 7.5, H47 

fish (RT) 96-h LC50 = 7.4 M, pH 6.6, H47 

fish (RT) 96-h LC50 = 14.6 M, pH 7.3, H47 

mean RT 96-h LC50 = 10.0 Predicted, n3 

fish (BT) 96-h LC50 = 3.6 M, pH 6.5, H? 

mean fish 96-h LC50 = 11.0 Predicted, n3 

daphnid (Cd) 48-h LC50 = 1.9 M, pH 7.4, H50 

daphnid (Cd) 48-h LC50 = 3.7 M, pH 7.7, H47 

mean Cd 48-h LC50 = 2.7 Predicted, n2 

daphnid (Dm) 48-h LC50 = 3.9 M, pH 7.0, H45 

daphnid (Dm) 48-h LC50 = 38.0 M, pH 7.1, H220 

mean Dm 48-h LC50 = 12.0 Predicted, n2 

mean daphnid 48-h LC50 = 5.7 Predicted, n2 
18 

OW FW Acute WQC = 1.5 

green algal 96-h EC50 = 0.570, Measured, pH 7.6, H15 

green algal 96-h EC50 = 0.460, Measured, p H8.2, H15 

mean algal 96-h EC50 = 0.510 Predicted, n2 

fish (FHM) ChV = 3.3 Measured, pH 7.7, H220 

fish (FHM) ACR = 11.0 Measured 

daphnid (Dm) ChV = 0.742 Measured, pH 8.3, H220 

daphnid (Dm) ChV = 0.320 Measured, pH 7.7, H45 

mean Dm ChV = 0.490 Predicted, n2 

Dm ACR = 24.0 Measured 

daphnid (Cd) ChV = 1.9 Measured, pH 7.2, H50 

Cd ACR = 1.4 Measured 

mean daphnid ChV = 0.970 Predicted, n2 

mean daphnid ACR = 5.9 Measured 

OW FW Chronic WQC = 0.087 

algal ChV = 0.100 Predicted, EC50/4 

Biological Fate

Fish (BT-eyed embryo) 30-d BCF (wb) = 50.0 Measured, pH 7.2, H242 

Fish (BT-fry) 30-d BCF (wb) = 136.0 Measured, pH 7.2, H242 

mean fish BCF = 93.0 Predicted, n2 

The toxicity profile for soluble inorganic complexes of Al can be predicted via MW adjustment 

of the toxicity for Al to the toxicity of the complex. 

Ca Al hydroxy phosphites [141 728-04-3]

Cax Al2(OH)2 (x+3-y) (HPO3)y @ mH2O with x = 2 to 12, (2x+5))2 >y>0, and m = 0 to 12; typical 

composition = 31% Ca, 9.5% Al, & 8.0% P; solid with mp >250 EC (dec); S = 680 mg/L; pH 

11.5; 

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

 Concentration (mg/L) 

Effect --------------------------------------- 

 Complex Al Notes 

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

fish 96-h LC50 120.0 11.0 Predicted 

fish 96-h LC50 409.0 6.0 Measured 

daphnid 48-h LC50 60.0 5.7 Predicted 

daphnid 48-h LC50 24.0 nm Measured 
19 

green algal 96-h EC50 5.4 0.510 Predicted 

fish ChV 35.0 3.3 Predicted 

daphnid ChV 10.0 0.970 Predicted 

algal ChV 1.0 0.100 Predicted 

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

Na Al fluoride [15 096-52-3]

sodium fluoaluminate; sodium fluoride aluminum; cryolite; kryolith; M12,2673; Na3 Al F6; 

MW210; composition: 13% Al; solid with mp 1000 EC; S = 610 mg/L with pH 6.2; used as an 

insecticide since 1929; 

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

Concentration (mg/L) 

Effect ---------------------------------------- 

Complex Al Notes 

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

fish 96-h LC50 85.0 11.0 Predicted 

fish 96-h LC50 21.0 2.8 Measured 

daphnid 48-h LC50 44.0 5.7 Predicted 

green algal 96-h EC50 3.9 0.510 Predicted 

fish ChV 25.0 3.3 Predicted 

daphnid ChV 7.5 0.970 Predicted 

algal ChV 0.770 0.100 Predicted 

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

The toxicity profile for chelates of Al with polyanionic monomers can be predicted via MW 

adjustment of the toxicity for Al to the toxicity of the chelate. 

The toxicity profile for organoAl compounds are developed for only the hydrolysis product(s) of 

Al. OrganoAl compounds are unstable in air and water. MethylAl and ethylAl are pyrophoric 

and dodecylAl slowly hydrolyses in water. 

Boundaries. The toxicity of Al compounds depends on their water solubility, the 

bioavailability of Al, and their stability. The most important property determining the toxicity 

of Al compounds is water solubility. Water solubility cannot be predicted accurately and has to 

be measured. Molecular weight (MW) is only important when Al complexes are water soluble 

and stable. Stable complexes of Al with MWs > 1000 are not expected to be absorbed by 

aquatic organisms and Al is not expected to be bioavailable even if they are water soluble. 

Therefore, only unstable Al compounds with MWs < 1000 are expected to be toxic. 

General Testing Strategy

Tier 1. Fate testing. Physical state (Harmonized Test Guideline 830.6303) and 
20 

corresponding property, i.e., melting point-melting point range (Harmonized Test Guideline 

830.7200) or boiling point-boiling point range (Harmonized Test Guideline 830.7220), water 

solubility (Harmonized Test Guideline 830.7840 or 7860), octanol/water partition coefficient 

(Kow) (Harmonized Test Guideline 830.7550, 7560 or 7570; or OECD 123, Partition Coefficient 

(1-Octanol/Water): Slow-Stirring Method), and vapor pressure (Harmonized Test Guideline 

830.7950); and/or 

Acute environmental toxicity testing. The aquatic base set of environmental toxicity tests will 

be recommended for aquatic exposures: fish acute toxicity, daphnid acute toxicity, and green 

algal toxicity. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and 

daphnids (Harmonized Test Guideline 850.1010) will be done using the static method; 

effective concentrations will be based on 100% active ingredients (ai) and nominal 

concentrations; the total organic carbon (TOC) concentration of dilution water in the control 

must be less than 2.0 mg TOC/L; TOC must be measured in the control just prior to the start of 

the test; the highest treatment concentration on a nominal-basis should not exceed the aqueous 

solubility limit of the tested compound; solvent can not be used; and hardness of dilution water 

has to be less than 180.0 mg/L as CaCO3. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 

the static method; effective concentrations based on 100% ai and nominal concentrations; 

statistical analysis of effective concentrations at 24, 48, 72, and 96 hours; test medium with no 

more than 0.300 mg/L EDTA as a final concentration; the TOC of the test/growth medium 

should be less than 2.0 mg TOC/L; TOC should be measured just prior to the start of the test; 

the highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit of the tested compound; and solvent can not used; . 

In addition fish-toxicity-mitigation testing (Harmonized Test Guideline 850.1085) with 

known amounts of humic acid (HA) added to dilution water, i.e., 20 mg HA/L and 10 mg HA/L, 

will be recommended. 

If there is no significant risk from the Al compound after the results of tier one testing set 

have been integrated into the risk assessment, then no further testing will be recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Fate testing. Aerobic biodegradability according to either of the following test 

guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

and/or 
21 

Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing (Harmonized Test 

Guideline 850.1400), with the flow-through method; effective concentrations based on 100% ai 

and mean measured concentrations of soluble Al; statistical analysis of effective concentrations 

at days 7, 14, 21, and 28; the TOC of dilution water in the control should be less than 2.0 mg 

TOC/L; TOC should be measured in the controls just prior to and during the test; the highest 

treatment concentration on a nominal-basis should not exceed the aqueous solubility limit of the 

tested compound; solvent can not be used; and hardness of dilution water has to be less than 

180.0 mg/L as CaCO3; and 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with the flow-through 

method; effective concentrations based on 100% ai and mean measured concentrations of soluble 

Al; statistical analysis of effective concentrations at days 7, 14, and 21; the TOC of dilution 

water in the control should not exceed 2.0 mg TOC/L; TOC must be measured in the controls 

just prior to and during the test; the highest treatment concentration on a nominal-basis should 

not exceed the aqueous solubility limit of the tested compound; solvent can not be used; and 

hardness of dilution water has to be less than 180.0 mg/L as CaCO3. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental 

toxicity tests will be recommended for terrestrial exposures. The terrestrial base set includes: 

the early seeding growth test (Harmonized Test Guideline 850.4230), the earthworm toxicity test 

(Harmonized Test Guideline 850.6200), the soil microbial community bioassay (Harmonized 

Test Guideline 850.5100), and the avian acute oral toxicity test (Harmonized Test Guideline 

850.2100). Chronic toxicity testing for terrestrial organisms include: the plant whole life cycle 

test (Harmonized Test Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 

850.4800), and the avian reproduction test (Harmonized Test Guideline 850.2300). 

Abbreviations.

ACR10 = acute-to-chronic ratio = 10; 

ai = active ingredients; 

BCF = bioconcentration factor; 

BT = brook trout; 

Cd = Ceriodaphnia; 

ChV = Chronic value; 

Dm = Daphnia magna; 

EC = effective concentration; 

FHM = fathead minnow; 

FT = flow-through method; 

FW = fresh water; 

H = hardness in mg CaCO3/L; 

H? = hardness unknown; 

LOEC = lowest-observed-effect concentration; 

M = measured concentrations; 

n# = sample size used in calculation of the mean; 

nm = not measured; 

NOEC = no-observed-effect concentration; 

OW = Office of Water; 
22 

P = predicted; 

RT = rainbow trout; 

S = static method; 

SAR = structure activity relationship; 

SR24 = static renewal method with renewals every 24 h; 

TOC = total organic carbon; 

Wb = whole body; 

WQC = water quality criterion;

August, 1997; revised June 2010 
23 

Category: Aminobenzothiazole Azo Dyes Human Health 

Environmental Toxicity 

Definition. Any disperse azo dye containing the substructure 2-aminobenzothiazole or 

2-(p-amino)phenylbenzothiazole, or phenyl ring-substituted derivatives of the same, is 

considered to be a member of the category. 

Hazard Concerns. There are oncogenicity/mutagenicity concerns for intact 

aminobenzothiazole azo dyes by analogy to dimethyl aminostyryl benzothiazole and Butter 

Yellow-type dyes, such as 4-ethyl-N,N-diethylaminoazobenzene. In addition, there are liver 

and thyroid concerns for reduction products by analogy to 2-aminothiazole, and neuro-toxicity 

concerns by analogy to chlorinated 2-aminobenzothiazole. Ecotoxicity concerns are generally 

chronic concerns only and are based on QSAR predictions for neutral organic compounds. 

Neutral organic compounds are an established ecotoxicity category, of which these dyes are part 

of the disperse dye subclass. 

Boundaries. The boundaries are not strictly defined. For a typical member of the category, 

R1 = N- and/or ring substituted p-aminophenyl groups, and R2 = halogens or nitro groups. 

General Testing Strategy

The New Chemicals Program considers the following tests to be the most appropriate for 

aminobenzothiazole azo dyes found to pose an unreasonable risk: 

- In vivo mouse micronucleus assay in bone marrow by the i.p. route (Harmonized Test 

Guideline 850.5395). 

- 90-day subchronic toxicity test in rats by the oral route, with special attention to the 

thyroid and liver (Harmonized Test Guideline 870.3100). 
24 

- Fish early life stage test (Harmonized Test Guideline 850.1400). 

- Chronic daphnid test (Harmonized Test Guideline 850.1300). 

- Algae toxicity test (Harmonized Test Guideline 850.5400). 

If the mouse micronucleus assay is positive, further characterization of the potential 

cancer risk may be recommended: 2-year cancer bioassay by the oral route in 2 species of 

rodents (Harmonized Test Guideline 870.4200). 

Potentially significant ecotoxicity risk, as well as human health risks, resulting from 

releases to water ONLY, may be addressed by environmental fate testing prior to the chronic 

ecotoxicity and human health testing. The results of the environmental fate testing may 

preclude the need for further testing. 

- Jar test to determine the settling rate and extent of removal of suspended solids from 

solution (draft protocol available). 

If the results of the jar test do not mitigate the health and/or ecotoxicity concerns, further 

characterization of the environmental fate of the dye may be recommended. 

January, 1992; revised June 2006. 
25 

Category: Anhydrides, Carboxylic Acid Human Health 

Definition. Any molecular structure containing one or more carboxylic acid anhydride groups 

is considered to be a member of the category for new chemical purposes. Members of the class 

include new carboxylic acid anhydrides as well as new oligomers, polymers, prepolymers, or 

reaction products of existing carboxylic acid anhydrides. As illustrated below, a typical new 

chemical carboxylic acid anhydride of concern is a polymer or oligomer containing a monomer 

such as maleic anhydride. 

Hazard Concerns. Carboxylic acid anhydrides are of concern for potential pulmonary 

sensitization based on data for phthalic, trimellitic, isopropylidene bis(phthalic), and sulfonyl 

bis(phthalic) anhydrides. Carboxylic acid anhydrides are also of concern for potential 

developmental or reproductive toxicity based on data for maleic, succinic, and phthalic 

anhydrides. 

Boundaries. Structures with a carboxylic acid anhydride equivalent weight of >5,000 are 

presumed not to pose a hazard under any conditions. Typically, concerns for health effects are 

confined to those species with molecular weights <1,000. 

The new chemical program has thus far been concerned only with those carboxylic acid 

anhydrides with potentially significant inhalation exposure, and has pursued developmental 

toxicity only for low molecular weight (<500) carboxylic acid anhydrides which are thought to 

have a significant potential for systemic uptake via the lung. For pulmonary sensitization, 

extensive systemic uptake may not be necessary for a biological response and we have therefore 

sought to regulate some oligomeric or polymeric carboxylic acid anhydrides only for that effect. 

General Testing Strategy

The following tests are usually prescribed for carboxylic acid anhydrides found to pose a 

potentially unreasonable risk: 

 - Pulmonary sensitization by either the method of Karol (Toxicol. Appl. Pharmacol. 

68:229-241, 1983), or an equivalent method. 

 - Oral developmental toxicity study in two species (Harmonized Test Guideline 

870.3700). 

May, 1991 
26 

Category: Anilines Environmental Toxicity 

Definition. This category includes all anilines, both monoanilines and polyanilines. It is 

assumed that these compounds need to be absorbed to be toxic; therefore, compounds with MWs 

> 1000 will be excluded from this category. Acute toxicity for anilines which are liquids at 

room temperature is known to be limited by the octanol/water partition coefficient (Kow). 

Above a log Kow value of ≥ 7.38, anilines show no effects at saturation during 96-h exposures 

(Veith and Broderius (1987). Anilines which are solids at room temperature may show no 

toxicity at saturation at lower Kow values depending on the melting point, i.e., the higher the 

melting point at a given Kow, the greater the likelihood that no toxicity will be observed at 

saturation. For solids, no effects at saturation should be determined on a case-by-case basis. 

There are no known Kow limits for chronic toxicity at this time, but it may not be much above a 

log Kow = 8 for liquid anilines. 

Hazard Concerns. Analysis of the aquatic toxicity for anilines has been reviewed in various 

publications and has been determined through SAR Analysis by EPA using ECOSAR – a hazard 

estimation tool that uses chemical structure descriptors to estimate the acute and chronic toxicity 

of a substance to aquatic organisms. [Link for ECOSAR: 

http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

Publications. Fish 96-h LC50 (Veith and Broderius 1987); fish 14-d LC50 (Deneer et al 1987); 

fish 14-d LC50 (Hermens et al 1984); daphnids 48-h LC100 (Nendza and Seydel 1988a and 

1988b); and green algal 96-h EC50 (Nendza and Seydel 1988a and 1988b). 

Aromatic diamines (i.e., two amines on one benzene) and dinitroanilines are known to be more 

toxic than predicted by these SARs. 

Members of this category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high 

toxicity (i.e., < 1 mg/L) depending on their Kow, MW and substitutions (e.g., dinitroanilines). 

Environmental Fate. Some studies have shown that certain anilines are subject to rapid direct 

and indirect photolysis under environmentally realistic conditions (Leifer 1990). 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW. Acute toxicity expected with log Kow < 7.38; no effects at saturation during 96-h 

exposures when log Kow ≥ 7.38. Chronic toxicity has no known upper bound for log Kow, but it 

is probably near 8. MW will be < 1000. The environmental base set of tests will be requested for 

aquatic releases and the terrestrial base set of tests will be recommended for terrestrial exposures. 

When the log Kow is ≥ 7.38, chronic toxicity testing with fish and daphnids will be 

recommended. 
27 

General Testing Strategy. 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for 

aquatic exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and 

daphnids (Harmonized Test Guideline 850.1010) will be done using the flow-through method 

with measured concentrations; effective concentrations will be based on 100% active ingredients 

(AI) and mean measured concentrations; measured TOC of dilution water in the control; the 

highest treatment concentration on a nominal-basis should equal the aqueous solubility limit; and 

solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be 

used to artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 

static methods; measured concentrations.; effective concentrations based on 100% active 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; the highest treatment concentration on a nominal-basis equal to the aqueous 

solubility limit; and solvent can be used to assist the PMN to reach its aqueous solubility limit 

quicker, but cannot be used to artificially enhance the water solubility of the PMN beyond its 

aqueous solubility limit. 

If there is no significant risk from the PMN after the results of the environmental base set 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water— Indirect Photolysis Screening 

Test (Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, go to 

Tier 4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then 

prepare a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. For example, the most 

sensitive species from the environmental base set has an EC50 value = 2.0 mg PMN/L (based on 

100% active ingredients [AI]), therefore, prepare a 5.0 mg PMN per liter stock solution based on 

100% AI using the standard humic-containing solution. This stock solution is exposed to 

sunlight for at least 6 half-lives to ensure that all of the PMN has been photolyzed, and then this 

stock solution is used to retest the most sensitive aquatic species to determine if the photolysis 

products of the PMN are more or less toxic that the PMN. 
28 

Tier 4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured 

TOC of dilution water in the control; the highest treatment concentration on a nominal-basis 

should be set at the aqueous solubility limit; solvent can be used to assist the PMN to reach its 

aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility of 

the PMN beyond its aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be 

substituted for the 28-d ELS toxicity test because Van Leeuwen et al (1990) have demonstrated 

that the 7-d ELS toxicity test underestimated the chronic toxicity of anilines measured by the 

28-d ELS toxicity test by >5.3 times when the NOECs were compared (see Table VII in Van 

Leeuwen). 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% 

active ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, and 21; measured TOC of dilution water in the control; the highest 

treatment concentration on a nominal-basis should be set at the aqueous solubility limit; solvent 

can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN beyond its aqueous solubility limit; and the 

7-d daphnid chronic toxicity test cannot be substituted for the 21-d toxicity test because Van 

Leeuwen et al (1990) have demonstrated that the fish 7-d ELS toxicity test underestimated the 

chronic toxicity of anilines measured by the fish 28-d ELS toxicity test by >5.3 times when the 

NOECs were compared (see Table VII in Van Leeuwen). 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200] and the soil microbial community bioassay 

[Harmonized Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic 

toxicity testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), and the soil 

microbial community bioassay (Harmonized Test Guideline 850.5100). 
29 

References. 

Deneer JW, Sinnige TL, Seinen W and Hermens JLM. 1987. Quantitative structure-activity 

relationships for the toxicity and bioconcentration factor of nitrobenzene derivatives towards the 

guppy (Poecilia reticulata). Aquatic Toxicology 10:115-129. 

Hermens J, Leeuwangh P, and Musch A. 1984. Quantitative structure-activity relationships 

and mixture toxicity studies of chloro- and alkylanilines at an acute lethal toxicity level to the 

guppy, Poecilia reticulata. Ecotoxicology and Environmental Safety 8:388-394. 

Leifer A. 1990 (14 Dec). Review of Section 5 test data for o-phenylenediamine, 

m-phenyldiamine, and p-phenylenediamine. Memorandum. Washington, DC: Exposure 

Assessment Branch, Exposure Evaluation Division (TS-798), Office of Toxic Substances, United 

Stated Environmental Protection Agency, 401 M St, SW, 20460-0001. 

Nendza M and Seydel JK. 1988a. Multivariate data analysis of various biological test 

systems used for the quantification of ecotoxic compounds. Quantitative Structure-Activity 

Relationships 7:165-174. 

Nendza M and Seydel JK. 1988b. Quantitative structure-activity relationships for 

ecotoxicologically relevant biotest systems and chemicals. Chemosphere 17:1585-1602. 

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

Veith GD and Broderius SJ. 1987. Structure-toxicity relationships for industrial chemicals 

causing type (II) narcosis syndrome. In Kaiser KLE (ed), QSAR In Environmental Toxicology 

-II, pp. 385-391. Reidel Publishing Company. 

May, 1991; revised June 2010 
30 

Subcategory of Anilines: Dianilines Human Health 

Environmental Toxicity 

Definition. A PMN must have the following minimum structural requirements to be considered 

a member of this category: 

1. The structure must have at least two phenyl rings with a bridging carbon, oxygen, 

nitrogen, or sulfur 

2. Each terminal phenyl ring must have a primary amino group (or a group that can 

be readily metabolized to a primary amino group) either meta- or para- to the 

bridging atom 

Compounds with one or more additional phenyl ring(s), with or without ring substituents, and 

one or more bridging atoms are also included in the category. 

Minimum Structure for Dianiline Category 

The compounds of greatest concern are those having X = C, N, or O and n = 0 or 1. 

Hazard Concerns. Members of the class are considered to be potential carcinogens and 

mutagens by analogy to 4,4'-methylendianiline, 4,4'-methylene bis(o-toluidine), and 

4,4'-oxydianiline. Class members are potential retinotoxic agents by analogy to 

4,4'-methylenedianiline, 4,4'-oxydianiline, and the diaminodiphenyl alkane drugs and are also 

potential reproductive and systemic toxicants by analogy to 4,4'-methylenedianiline. 
31 

General Testing Strategy

The New Chemicals Program has considered the following toxicity tests to be the most 

appropriate for dianilines found to pose an unreasonable risk: 

I. Exposure to Humans

- Rat acute oral retinopathy screening study (protocol to be approved by EPA) 

- Pigmented rat 90-day subchronic toxicity study by the oral route (Harmonized Test 

Guideline 870.3100) or inhalation route (Harmonized Test Guideline 870.3465) to 

include histopathological examination of the eyes and reproductive organs (eyes to be 

examined by both light and electron microscopy) 

- 2-year carcinogenicity bioassay (Harmonized Test Guideline 870.4200) in rats and mice 

In the 90-day subchronic toxicity study, the company may opt to carry a group of animals 

at each dose level for a 90-day recovery period to determine whether potential retinopathy is 

reversible. 

For some compounds in this class, short-term mutagenicity testing may be appropriate. 

When appropriate, specific testing will be determined by EPA mutagenicity assessors on a case 

by case basis by referral to "short question." 

Where the general population is at a significant risk from drinking water exposure (via 

surface water releases) to PMN chemicals of this class, the following fate testing may be 

appropriate: 

- Phototransformation of Chemicals in Water— Indirect Photolysis Screening Test 

(Harmonized Test Guideline 835.5270) 

 - Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test 

Guideline 835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized 

Test Guideline 835.3140) 

(See aniline category description for details) 

Results of the above fate tests may mitigate concern for drinking water exposure to PMN 

of this class. However, fate test results WILL NOT CHANGE AGENCY CONCERNS FOR 

OCCUPATIONAL EXPOSURE to PMNs of this category. 
32 

II. Release to Aquatic Ecosystems

Tier 1. Because of the above boundary conditions, and the need to assess human 

exposure as well as environmental toxicity, if there is insufficient knowledge about the water 

solubility of the dye, then it should be measured (Harmonized Test Guideline 830.7860). The 

fish and daphnid acute toxicity tests from the aquatic base set of environmental toxicity tests will 

be recommended for aquatic exposures. The acute toxicity tests for fish (Harmonized Test 

Guideline 850.1075) and daphnids (Harmonized Test Guideline 850.1010) will be done using the 

flow-through method with measured concentrations, and effective concentrations will be based 

on 100% active ingredients (AI) and mean measured concentrations. 

If there is no significant risk from the PMN after the results of the fish and daphnid acute 

toxicity tests have been integrated into the risk assessment, then no further testing is 

recommended. However, if there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water— Indirect Photolysis Screening 

Test (Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, go 

to Tier 4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then 

prepare a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. 

Tier 4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; and statistical analysis of effective concentrations at days 7, 14, 21, and 28. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% 

active ingredients (AI) and mean measured concentrations; and statistical analysis of effective 

concentrations at days 7, 14, and 21. 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 
33 

III. Release to Terrestrial Ecosystems: 

The terrestrial base set of environmental toxicity tests (i.e., the early seedling growth test 

[Harmonized Test Guideline 850.4230], the earthworm toxicity test [Harmonized Test Guideline 

850.6200] and the soil microbial community bioassay [Harmonized Test Guideline850.5100]) 

will be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial 

organisms include: the plant whole life cycle test (Harmonized Test Guideline 850.4150), the 

plant uptake test (Harmonized Test Guideline 850.4800), and the soil microbial community 

bioassay (Harmonized Test Guideline 850.5100). 

References

American Dye Manufacturers Institute, Inc. (1974). "Dyes and the Environment: Reports on 

Selected Dyes and Their Effects," Vol. II, ADMI, New York. 

Auer, C.M., Nabholz, J.V. and Baetcke, K.P. (1990). "Mode of Action and the Assessment of 

Chemical Hazards in the Presence of Limited Data: Use of Structure-Activity Relationships 

(SAR) under TSCA, Section 5," Environmental Health Perspectives, Vol. 87, pp. 183-197. 

Little, L.W., and Lamb J.C., III (1972). "Acute Toxicity of 46 Selected Dyes to the Fathead 

Minnow, Pimephales promelas, "Final Report to the American Dye Manufacturers Institute, Inc., 

UNC Wastewater Research Center, Department of Environmental Sciences and Engineering, 

School of Public Health, University of North Carolina, Chapel Hill, NC. 

Nabholz, J.V. (1990). "The OTS PMN ECOTOX Data Base: a Confidential Business 

Information (CBI) Collection of Environmental Toxicity Data from New Chemical Submissions 

Under Sec. 5," Unpublished, Environmental Effects Branch, Health and Environmental Review 

Division (TS-796), U. S. Environmental Protection Agency, Washington, DC. 

Sigman, C.C., Helms, C.T., Papa, P.A., Atkinson, D.L., Doeltz, M.K., and Winship-Ball, A. (Jan. 

1983). "Anthraquinone Dyes and Related Chemicals: Review and Assessment of Potential 

Environmental and Health Aspects," Final Report to the Dyes Environmental and Toxicology 

Organization, Inc., SRI International, Menlo Park, CA. 

Tonogai, Y., Ito, Y., Iwaida, M., Tati, M., Ose, Y., and Sato, T. (1979). "Studies on the Toxicity 

of Coal-Tar Dyes. II. Examination of the Biological Reaction of Coal-Tar Dyes to Vital Body," 

The Journal of Toxicological Sciences, Vol. 4, pp. 211-219. 

August 1991; revised January 1995; revised October 1995; revised June 2010 
34 

Category: Anionic Surfactants Environmental Toxicity 

Definition. Any molecular structure with a net negative charge and having surfactant activity 

is a member of this category. The category includes for example, alkyl sulfonates, alkyl 

benzene sulfonates, alkyl silicic acids, alkyl phosphates, alkyl carboxylic acids, or combinations 

of these anionic groups, e.g., alkyl sulfonate with carboxylic acid substitutions. 

Hazard Concerns. Anionic surfactants are toxic to a wide variety of aquatic organisms. 

Toxicity increases exponentially with increasing carbon chain length up to 16 carbons [for linear 

alkyl sulfonate (LAS) surfactants], and then decreases with additional carbons. At a chain 

length of 16 carbons, fish and daphnids are most sensitive, but at lower chain lengths green algae 

are more sensitive than fish and daphnids. There are a number of structure-activity 

relationships (SARs) to predict the toxicity of members of this category. Most are parabolic 

regression equations and others rely on nearest analog methodology. 

Boundaries. There is no molecular weight boundary. Surfactants with molecular weights > 

1000 are still toxic. Acute toxicity may be low, i.e., > 100 mg/L, if a strong cationic surfactant 

counterion and the anionic surfactant form a tight ion pair. 

Testing. To address ecotoxicity concerns, base set acute aquatic toxicity testing (green algae: 

static method, daphnid and fish: flow-through method, all measured concentrations). 

Tier 1. The acute aquatic base set of environmental toxicity tests will be recommended 

for aquatic exposures and the terrestrial base set of environmental toxicity tests (i.e., the early 

seedling growth test, the earthworm acute toxicity test and the soil microbial community 

bioassay) will be recommended for any terrestrial exposures. 

Acute fish toxicity test Harmonized Test Guideline 850.1075 

Acute daphnid toxicity test Harmonized Test Guideline 850.1010 

Green algae toxicity test Harmonized Test Guideline 850.5400 
35 

Early seedling growth test Harmonized Test Guideline 850.4230 

Earthworm acute toxicity test Harmonized Test Guideline 850.6200 

Soil microbial community bioassay Harmonized Test Guideline 850.5100 

Tier 2. If acute toxicity testing indicates a significant risk, then environmental fate 

testing in the form of aerobic biodegradation testing is recommended according to either of the 

following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

Tier 3. In addition, if acute toxicity testing indicates a significant risk, then chronic 

aquatic toxicity testing with fish and aquatic invertebrates will be recommended. 

Fish early life stage test Harmonized Test Guideline 850.1400 

Daphnid chronic toxicity testing Harmonized Test Guideline 850.1300 

September 1988; revised September, 1996; revised June 2010 
36 

Category: Azides Environmental Toxicity 

Definition. Azides are a class of chemicals consisting of both inorganic and organic 

compounds and characterized by the functional group N=N=N. Substitutions may be either 

metals or organic compounds, e.g., acetic acid and benzene. So far, only monomeric aromatic 

azide compounds have been submitted as PMNs. No aliphatic azides, e.g., alkyl azides, have 

been submitted as PMNs. Aliphatic azides may be too explosive to isolate, however, 

diazidoacetic acid ester is known to exist and has been tested in rats. 

Hazard Concerns. It is assumed that azides have to be absorbed to be toxic, therefore, azides 

with MW >1000 will be excluded from this category. Acute toxicity for monomeric azides is 

assumed to be correlated and limited by the octanol/water partition coefficient (Kow). Above a 

log Kow value of >5.0, azides are assumed to show no effects at saturation during 96-hour 

exposures to fish. Organic azides which are solids at room temperature may show no toxicity at 

saturation at lower Kow values depending on their melting point and/or their water solubility. 

For example, for organic azides, the higher the melting point at a given Kow, the greater the 

likelihood that no toxicity will be occur at saturation. For solids, no effects at saturation has to 

be determined on a case-by-case basis. The upper Kow limits for chronic toxicity are 

approximately log Kow = 8. 

The toxicity for inorganic azides has to be determined by integrating the toxicity of Na azide 

with the toxicity of any other inorganic element, e.g., Pb, with a MW adjustment for differences 

in toxicity between Na azide and the other inorganic element. Na azide [26628-22-8] has been 

tested by the USEPA ERL-Duluth: fathead minnow 96-h LC50 = 5.46 mg/L based on a 

flow-through method with nominal concentrations. 

The SAR for organic azides is based on (1) sodium azide value, (2) a calculated log Kow, and (3) 

no acute effects to fish at saturation assumed to occur at a log Kow >5.0 which is equivalent to a 

log fish 96-h LC50 = -2.5 in millimoles per liter. 

Environmental Fate: Na azide is known to hydrolyze in water to form hydrazoic acid (or 

hydrogen azide, NH3, [7782-79-8], MW43, M12,4815). Hydrogen azide is extremely explosive 

according to Merck. In addition, azides can be transformed to nitrenes by uv light. 

Boundaries: MW <1000. Log Kow <5.0 for acute toxicity to fish and aquatic invertebrates; 

log Kow <6.4 for toxicity to green algae as a 96-h EC50; and log Kow assumed to be <8.0 for 

chronic toxicity to aquatic organisms, but could be higher. 
37 

General Testing Strategy:

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for 

aquatic exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and 

daphnids (Harmonized Test Guideline 850.1010) will be done using the flow-through method 

with measured concentrations; effective concentrations will be based on 100% active ingredients 

(ai) and mean measured concentrations; measured TOC of dilution water in the control; ideally, 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; and solvent can be used to assist the aldehyde to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the test 

chemical significantly above its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 

static methods; measured concentrations; effective concentrations based on 100% active 

ingredients (ai) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; ideally, mean measured concentrations in the highest treatment concentration 

should be equal the aqueous solubility limit; and solvent can be used to assist the aldehyde to 

reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the water 

solubility of the test chemical significantly above its aqueous solubility limit. 

If there is no significant risk from the PMN chemical after the results of the 

environmental base set have been integrated into the risk assessment, then no further testing is 

recommended. However, if there is a significant risk, then go to Tier 2. 

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the PMN chemical after the results of biodegradation 

testing have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; 

measured TOC of dilution water in the control; ideally, mean measured concentrations in the 
38 

highest treatment concentration should be equal the aqueous solubility limit; solvent can be used 

to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially 

enhance the water solubility of the PMN significantly above its aqueous solubility limit; and the 

7-d ELS stage toxicity test cannot be substituted for the 28-d ELS toxicity test because the 7-d 

ELS toxicity test may underestimate chronic toxicity measured by the 28-d ELS toxicity test 

when the Chronic Values are compared. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% 

active ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, and 21; measured TOC of dilution water in the control; ideally, 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; solvent can be used to assist the PMN to reach its aqueous solubility 

limit quicker, but cannot be used to artificially enhance the water solubility of the PMN 

significantly above its aqueous solubility limit; and the 7-d daphnid short-term chronic toxicity 

test cannot be substituted for the 21-d toxicity test because the daphnid 7-d short-term toxicity 

test may underestimate chronic toxicity measured by the 21-d toxicity test when the chronic 

values are compared. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seeding growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200], and the soil microbial community bioassay 

[Harmonized Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic 

toxicity testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), and the soil 

microbial community bioassay (Harmonized Test Guideline 850.5100). 

References:

Abbe, G. (1969). Decomposition and addition reactions of organic azides. Chemical

Review, 69, 345-363. 

Scriven, E.F. (Ed.). (1984). Azides and nitrenes: Reactivity and utility. pp.95-204. New 

York: Academic Press. 

September 1996; revised June 2010; revised June 2010 
39 

Category: Benzotriazoles Environmental Toxicity 

Definition. This category includes all benzotriazoles. 

Hazard Concerns. The toxicity for benzotriazoles with -NH has been determined through 

SAR Analysis (Clements 1988). Benzotriazoles with -NH are known to be more toxic than 

neutral organic chemicals, and this excess toxicity decreases with increasing Kow. The toxicity 

of benzotriazoles with aliphatic substitutions on the nitrogen are expected to act like neutral 

organic compounds. Other substitutions on the N, e.g., -SH, may be evaluated on a 

case-by-case basis. 

Members of this category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high 

toxicity (i.e., < 1 mg/L) depending on their Kow, MW, and melting point. 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow, MW, and melting point (mp). These compounds need to be absorbed to be toxic; therefore, 

compounds with MWs < 1000 are expected to cause toxicity, while compounds with MWs > 

1000 are no expected to show toxicity at saturation. 

Acute toxicity for benzotriazoles which are liquids at room temperature is known to be limited 

by the octanol/water partition coefficient (Kow). Above a log Kow value of 5.0, benzotriazoles 

typically show no effects at saturation during 96-h exposures (Clements 1988). Benzotriazoles 

which are solids at room temperature may show no toxicity at saturation at lower Kow values 

depending on the melting point, i.e., the higher the melting point at a given Kow, the greater the 

likelihood that no acute toxicity will be observed at saturation. For solids, the 

no-effects-at-saturation point for acute toxicity has to be determined on a case-by-case basis. 

The log Kow limit for chronic toxicity is set at 8 for liquid benzotriazoles. For solids, chronic 

toxicity testing will determine the Kow limit. 

Therefore, acute toxicity is expected when log Kow ≤ 5.0 and MW < 1000; no effects at 

saturation during 96-h exposures are expected when log Kow > 5.0 and MW < 1000. The upper 

boundary for chronic toxicity is typically 8.0. Only chronic toxicity is expected when log Kow

> 5.0 and < 8.0, and MW < 1000. Whenever MW > 1000, no effects are expected at saturation 

because it is assumed that benzotriazoles have to be absorbed to be toxic. 

Aerobic biodegradation is expected to be the dominant route of transformation in the 

environment. 
40 

General Testing Strategy.

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for 

aquatic exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and 

daphnids (Harmonized Test Guideline 850.1010) will be done using the flow-through method 

with measured concentrations; effective concentrations will be based on 100% active ingredients 

(AI) and mean measured concentrations; the highest treatment concentration on a nominal-basis 

should not exceed the aqueous solubility limit of the tested chemical; and solvent can be used to 

assist the chemical to reach its aqueous solubility limit quicker, but cannot be used to artificially 

enhance the water solubility of the chemical beyond its aqueous solubility limit. 

The algal toxicity test (Harmonized Test Guideline 850.5400) should be done with the 

static method; measured concentrations; effective concentrations based on 100% active 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; the highest treatment concentration on a nominal-basis should not exceed the 

aqueous solubility limit of the chemical; and solvent can be used to assist the chemical to reach 

its aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility 

of the chemical beyond its aqueous solubility limit. 

If there is no significant risk from the benzotriazole after the results of the environmental 

base set have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the benzotriazole after the results of the aerobic 

biodegradation testing have been integrated into the risk assessment, then no further testing is 

recommended. However, if there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; the 

highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit for the chemical; solvent can be used to assist the chemical to reach its aqueous solubility 

limit quicker, but cannot be used to artificially enhance the water solubility of the chemical 

beyond its aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be substituted for 
41 

the 28-d ELS toxicity test because Van Leeuwen et al (1990) have demonstrated that the 7-d 

ELS toxicity test underestimated the chronic toxicity of anilines measured by the 28-d ELS 

toxicity test by >5.3 times when the NOECs were compared (see Table VII in Van Leeuwen). 

Both anilines and benzotriazoles with -NH are more toxic than predicted based on narcosis alone, 

i.e., both benzotriazoles and anilines have excess toxicity due to a more specific mode(s) of toxic 

action. A seven day exposure may not allow enough time for this excess toxicity to be 

expressed either because of not enough exposure and/or not enough time for metabolic 

activation. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% 

active ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, and 21; the highest treatment concentration on a nominal-basis 

should not exceed the aqueous solubility limit of the chemical; solvent can be used to assist the 

chemical to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance 

the water solubility of the chemical above its aqueous solubility limit; and the 7-d daphnid 

chronic toxicity test cannot be substituted for the 21-d toxicity test (Van Leeuwen et al 1990). 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200], the avian acute oral toxicity test 

[Harmonized Test Guideline 850.2100], and the soil microbial community bioassay [Harmonized 

Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic toxicity 

testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), the avian 

reproductive toxicity test (Harmonized Test Guideline 850.2300), and the soil microbial 

community bioassay (Harmonized Test Guideline 850.5100). 

References

Clements, RG (editor). 1988. Estimating toxicity of industrial chemicals to aquatic organisms 

using structure-activity relationships. EPA-560-6-88-001. Washington, DC: Environmental 

Effects Branch, Health and Environmental Review Division, Office of Toxic Substances 

(TS-796), United States Environmental Protection Agency. Available from the National 

Technical Information Service, Springfield, VA 22161, PB89-117592. 

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

March, 1992; revised June 2010
42 

Category: Benzotriazole-hindered phenols Human Health 

Environmental Toxicity 

(see Phenols) 

Definition. Any molecular structure containing the following substructure is considered to be a 

member of the category. The predominant use of members of this category is as a UV light 

stabilizer in coating or plastic formulations. 

Note: Health effects may vary depending on the nature of the ring substituents. 

Hazard Concerns.

I. Health 

Systemic toxicity based on 8(e) and PMN data on analogues. These data are generally 

consistent across compounds, with the following endpoints occurring in subacute, subchronic, 

and chronic oral feeding studies in rats and dogs in which doses ranged from 5 to 15,000 ppm. 

Increased organ weights (liver and kidney, with associated histopathology at higher doses); 

hematological effects (decreased hemoglobin, packed cell volume, and erythrocytes); and 

immune system effects (weight changes in thymus, spleen, lymph nodes; decreased leukocytes). 

 Generally, treatment-related effects are dose-related, increasing in frequency and severity with 

increasing dose. Males appear to be more sensitive than females, and similar toxic effects 

occur in both rats and dogs. 

The lowest available NOAEL for systemic effects, from a 90-day rat study, is 5 ppm, or 0.25 

mg/kg/day. 

Reproductive toxicity - Concern is also based on 8(e) and PMN data on analogues. As with 

systemic toxiciy, the data are generally consistent with the following endpoints occurring in 

subacute and subchronic oral feeding studies in rats and dogs in which doses ranged from 5 to 
43 

15,000 ppm. 

Atrophy of the seminal vesicles, significant reduction in absolute and relative testes weight, 

significant reduction in absolute and relative prostate weight, and abnormal spermatogenesis. 

A subchronic dog study also provided evidence of female reproductive toxicity. 

Generally, treatment-related effects are dose-related, increasing in both frequency and severity 

with increasing dose. Males appear to be more sensitive than females, and similar toxic effects 

occur in both rats and dogs. 

The lowest NOAEL for reproductive toxicity, from a 90-day dog study, is 15 mg/kg/day. 

Dermal sensitization - Dermal sensitization test data were positive in 3/4 compounds tested. 

Two of the compounds showed strong sensitizing potential based on results obtained from 

maximization tests in which 70% and 90% of the treated guinea pigs became sensitized, 

respectively. 

II. Environmental 

The environmental concerns for the substances described in this category have already been 

described in the Phenol category. 

Boundaries. Not enough is known about the structure-activity relationships of these 

compounds to set any boundaries on members of the category; compounds with both "small" and 

"large" substituents have shown effects, and the effects are generally consistent from compound 

to compound. 

General Testing Strategy

I. Health 

Systemic Toxicity and Reproductive Toxicity. A 90-day gavage study in rats with special 

attention to hematology; weight and histopathology of lymphoid organs (spleen, thymus, and 

bone marrow); cellularity of the bone marrow, thymus, and spleen; and histopathology of the 

liver, kidney, heart, and all endocrine glands for which weight changes are observed. Particular 

attention should be directed toward achieving satisfactory quality from fixation and embedding 

of the testes, following the recommendations of Russell et al. [Russell LD, Ettlin RA, Sinha 

Hikim AP, Clegg ED. 1990. Histological and histopathological evaluation of the testis. Cache 

River Press, Clearwater, FL]. 

A gavage study, as opposed to an oral feeding study, is recommended because decreased 

body weight gain, final body weight, and/or food consumption have been reported in some oral 

feeding studies with analogues. 
44 

If immunopathology and hematology in the 90-day study support the concern for adverse 

effects of the PMN substances on the immune system, then a further battery of tests, such as the 

NTP's Immunotoxicology Tier II Screening Panel, will be recommended. 

Dermal Sensitization. Because dermal sensitization is not routinely pursued under TSCA 5(e) 

as a regulatory endpoint, testing is not recommended. A letter may be sent to the PMN 

submitter expressing the Agency's belief that the compounds are likely to be dermal sensitizers 

and that protective measures should be taken for workers. 

II. Environmental Toxicity 

If exposure to the aquatic environment demonstrates a potential risk, testing of the 

substances described in this category is the same as that prescribed for the Phenols category. 

June, 1993. 
45 

Category: Boron Compounds Human Health 

Environmental Toxicity 

Definition. This category includes borates, organoborates, borate esters, boron hydrides, 

boranes, and boroxines. 

I. Human Health

Hazard Concerns. Reproductive toxicity (males/females), blood toxicity, and neurotoxicity. 

The Agency has an oral RfD for boron of 0.09 mg/kg/day (uncertainty factor 100) based on the 

finding of testicular atrophy and spermatogenic arrest in dogs in a 2-yr feeding study (Weir and 

Fisher 1972, as summarized in IRIS 1995). [All toxicity information presented here are 

summarized in an assessment of various aqueous cleaner chemicals prepared in 1990 for the 

Office of Air and Radiation. Reproductive toxicity information is also summarized in IRIS 

1995.] 

Reproductive Toxicity. The most significant effect seen in animals is reproductive toxicity (i.e., 

sterility in males and females, and testicular atrophy in males). A three-generation reproductive 

study in rats demonstrated sterility in males (lack of spermatozoa in atrophied testes) and 

females (decreased ovulation) after exposure to 58.5 mg boron/kg in the diet. NOAEL (rats) 

17.5 mg boron/kg. Sterility was also found in males (at 50 or 100 mg boron/kg) in a serial 

mating adjunct to a 60-day feeding study; NOAEL (rats) 25 mg boron/kg. 

Data from oral subchronic and chronic studies in rats, dogs, and mice also provide evidence that 

boron produces adverse effects on the male reproductive system. A statistically significant 

reduction in relative and absolute testes weights was seen in a 2-yr and a 90-day dietary study in 

male rats at 58.5 and 26.3 mg boron/kg, respectively. NOAEL=s (rats) 17.5 and 8.8 mg 

boron/kg, respectively. In male rats, dietary exposure to 50 mg/kg boron resulted in a 

significant reduction in fertility, a significant reduction in epididymal weight, and a reduction in 

sperm number after 30 days of treatment. A significant reduction in testicular weight and 

further reduction in sperm occurred after 60 days of treatment. NOAEL (rats) 25 mg boron/kg. 

 Similar results were observed in several drinking water studies in rats. 

In male dogs, dietary exposure to 29.4 mg boron/kg for 2 yr resulted in severe testicular atrophy 

and spermatogenic arrest. NOAEL (dogs) 8.8 mg boron/kg. In male and female dogs, dietary 

exposure to 43.8 and 4.4 mg boron/kg for 90 days did not affect the female reproductive system, 

but produced decreased testes weights (statistically significant at 43.8 mg boron/kg). NOAEL 

(dogs) 0.4 mg boron/kg. In male mice, dietary exposure to 131 mg boron/kg for 103 wk (only 

dose tested) caused an increased incidence of testicular atrophy and interstitial hyperplasia. 

Blood Toxicity. In a chronic feeding study in rats, packed cell volume and hemoglobin levels 

were significantly decreased in males and females at 58.5 mg boron/kg. NOAEL (rats) 17.5 mg 

boron/kg. In a subchronic drinking water study in rats, a significant decrease in plasma 
46 

triglyceride levels was noted at 23.7 and 47.4 mg boron/kg (only doses tested). LOAEL (rats) 

23.7 mg boron/kg. In a subchronic feeding study in dogs, 43.8 mg boron/kg but not 4.4 or 0.4 

mg boron/kg produced decreased packed cell volumes and hemoglobin levels. NOAEL (dogs) 

4.4 mg boron/kg. In a subchronic feeding study in mice, minimal to mild extramedullary 

hematopoiesis of the spleen was observed in all dosed groups (ca. 34, 68, 136, 272, or 544 mg 

boron/kg). LOAEL (mice) 34 mg boron/kg. There is also a case study in which an infant 

exposed to 43 mg boron/kg/day for 12 weeks developed anemia. 

Neurotoxicity. Ingestion of borax by human infants results in neurotoxicity. Case reports of 

nine infants who were exposed by sucking pacifiers dipped in a borax-honey mixture document 

similar findings of neurological symptoms (not specified) and seizures. For seven infants, 

doses are reported as 2 to 3 g borax/wk for 4 to 10 wk (ca. 4 to 16 mg boron/kg/day). Serum 

boron levels measured in three of the seven infants were elevated. For the other two infants, 

doses are reported as 125 mg borax/kg over a 12-wk period and 9 g borax over a 5-wk period (ca. 

43 and 8 mg boron/kg/day, respectively). The effects appear to be reversible upon cessation of 

exposure. Neurotoxicity testing is not recommended because animal studies do not appear to be 

predictive of this effect. 

Boundaries. The boundaries of this category are not yet well defined for health effects. All 

of the toxicity data are on boric acid or borax. A molecular weight cutoff of 1,000 is proposed, 

but there is no information from available toxicity data on a proper water solubility cutoff. 

General Testing Strategy. The OECD reproductive toxicity screen (OECD 421) with special 

additional attention to hematology. If this screen is positive for reproductive toxicity, a 

reproductive fertility study in rats according to Harmonized Test Guideline 870.3800 is 

recommended. 

In cases in which exposures are exclusively dermal, a dermal absorption study (either in vivo or 

in vitro) could be conducted to refine the dermal risk assessment. If the in vivo study is 

selected, the test material should not be corrosive. If there is some uncertainty as to the 

corrosivity of the neat test material, a dermal irritation study should be undertaken first. If the 

neat material is corrosive, dilution to a noncorrosive concentration with a vehicle such as acetone 

or the alcohol used to make the ester is recommended. 

II. Environmental Toxicity

Most of the toxicity information for boron compounds is for boric acid and sodium tetraborate. 

These boron compounds show low acute toxicity towards fish (250.0 mg/L as a mean acute 

toxicity value) and daphnids (70.0 mg/L as a mean acute toxicity value), but moderate toxicity 

towards green algae (20.0 mg/L as a mean EC50 value). However, these compounds exhibit 

large acute to chronic ratios (ACR) towards fish (125 as a mean ACR) and the difference 

between the EC50 value and the chronic value (ChV) in green algae is large (about 117 as a 

mean difference). The mean ACR for daphnids is 8. The mean ChVs for fish, daphnids, and 
47 

green algae are 2.0 mg/L, 9.0 mg/L, and 0.170 mg/L, respectively. Green algae appears to be 

the most sensitive group of species with respect to boric acid and sodium tetraborate. 

There are only screening data for fish for borate esters, specifically, only for tributylborate. 

These screening data showed no effects at 10.0 mg/L for 24 hours towards three species of fish. 

However, the purity of the tributylborate was not given. 

The only data for boranes are for tert-butylamine borane. These data are: fish 96-h LC50 = 

13.0 mg/L, daphnid 96-h LC50 = 0.700 mg/L, green algal 7-d EC50 = 3.0 mg/L, and algal ChV 

= 0.300 mg/L. 

The only toxicity information for boron hydrides are for mammals. These data show that all 

boron hydrides are highly toxic and more toxic than borates. 

The major environmental hazard concerns for this category are for chronic toxicity towards fish 

and toxicity towards green algae. 

Since there are no SARs for boron compounds, hazard profiles are developed using the nearest 

analog(s). 

Boundaries. Boron compounds must have water solubilities equal to or greater than 1.0 μg/L 

(ppb) and molecular weights generally need to be near or below 1000. 

Environmental Fate. Certain borates are subject to hydrolysis under environmentally realistic 

conditions. 

General Testing Strategy. 

The following testing strategy will address aquatic toxicity concerns: 

I. Release to Aquatic Ecosystems: 

Tier 1a. If the hydrolysis rate for any member of this class is predicted to be slow (t1/2 > 2 

days) or if hydrolysis will result in one or more products which are expected to be just as toxic as 

the parent borate, then the fish and daphnid acute toxicity tests from the aquatic base set of 

environmental toxicity tests will be recommended for aquatic exposures. The acute toxicity tests 

for fish (Harmonized Test Guideline 850.1075) and daphnids (Harmonized Test Guideline 

850.1010) will be done using the flow-through method with measured concentrations; effective 

concentrations will be based on 100% active ingredients (AI) and mean measured 

concentrations; measured TOC of dilution water in the control; the highest treatment 

concentration on a nominal-basis should equal the aqueous solubility limit; and solvent can be 

used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 
48 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the 

highest treatment concentration on a nominal-basis equal to the aqueous solubility limit; and 

solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be 

used to artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

If there is no significant risk from the PMN after the results of the environmental base set of tests 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 1b. If the hydrolysis rate for any member of this class is predicted to be rapid (t1/2 < 2 

days) and if hydrolysis will result in products which are expected to be significantly less toxic as 

the parent borate, then hydrolysis testing (Harmonized Test Guideline 835.2120) will be 

recommended. 

If the resulting hydrolysis t1/2 is < 2 days, then this result will be integrated into a new risk 

assessment for the PMN. However, the resulting hydrolysis t1/2 > 2 days, then the 

environmental base set will be recommended. 

If there is no significant risk from the PMN after the results of the environmental base set of tests 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; and statistical analysis of effective concentrations at days 7, 14, 21, and 28. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21. 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 
49 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200] and the soil microbial community bioassay 

[Harmonized Test Guideline 850.5100]) will be recommended for terrestrial exposures. 

Chronic toxicity testing for terrestrial organisms include: the plant whole life cycle test 

(Harmonized Test Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 

850.4800), and the soil microbial community bioassay (Harmonized Test Guideline 850.5100). 

July, 1991; revised August, 1997; revised June 2010. 
50 

Category: Cationic Dyes Environmental Toxicity 

Definition. Any dye bearing one or more net permanent positive charges is considered to be a 

member of this class. A "typical" new chemical of concern is a water soluble monoazo dye 

with a single delocalized positive charge. 

Hazard Concerns. Water soluble cationic dyes are toxic to fish, daphnids, and algae. Poorly 

soluble dyes tend to be toxic only to algae. No relationship between structure and activity has 

been found for cationic dyes. 

Boundaries. There are no established boundaries for cationic dyes. There is no molecular 

weight threshold - one dye with a molecular weight of 3,000 and bearing four positive charges 

was found to be toxic to fish. 

Testing. To address environmental concerns, the base set of environmental toxicity tests (i.e., 

the fish acute toxicity test, the daphnid acute toxicity test and the green algal toxicity test) is 

recommended. These tests are to be done using the static method and nominal concentrations. 

In addition, two additional fish acute toxicity tests are recommended with known amounts of 

humic acid added to the dilution water. This testing is necessary to measure the mitigating 

effects of dissolved organic carbon (DOC) on the toxicity of the cationic dye. One test will be 

done with 20 mg humic acid/L in dilution and the second test will have 10 mg humic acid/L in 

dilution water. Total organic carbon (TOC) will be measured three times in each test and the 

TOC of the clean dilution water will also be measured at the beginning of the test. 

If DOC mitigates the environmental risk to water column organisms, then testing using natural 

sediments and organisms known to ingest sediment may be recommended. 

March, 1990 
51 

Category: Cationic (quaternary ammonium) surfactants Environmental Toxicity 

Definition. 

Any cationic surfactant is a member of this category, for example: 

 CH3

 | 

 CH3-N+-(CH2-)15-CH3 Br- 

 | 

 CH3

 

Hazard Concerns. Cationic surfactants are biocidal to a wide array of species in the 

environment. Toxicity increases exponentially with increasing carbon chain length up to 16 

carbons and then decreases with increasing chain length. QSAR (quantitative structure-activity 

relationships) have been developed to predict toxicity. 

Boundaries. Little toxicity is observed when the carbon chain length exceeds 22. Tight ion 

pairs will not be significantly toxic. 

General Testing Strategy. To address ecotoxicity concerns, base set aquatic toxicity testing in 

algae, daphnids, and fish, plus humic acid testing in fish (20 mg/L and 10 mg/l humic acid in 

dilution water) is recommended. All testing uses static method, nominal concentrations. 

March, 1990 
52 

Category: Cobalt Environmental Toxicity 

This category includes but is not limited to inorganic and organic compounds of cobalt (Co), e.g., 

soluble cobalt cations, cobalt esters, and organocobalt compounds. 

Hazard Concerns. 

Most of the toxicity information for inorganic cobalt compounds is for the soluble salts: 

chloride, nitrate, and sulfate. There are no known data for organoCo compounds, organic acid 

chelates with Co, or for Co esters. 

The best toxicity data for Co are listed below with predicted (P) and measured (M) toxicity 

values indicated and effective concentrations in mg Co/L (ppm): 

fish (FHM) 96-h LC50 = 48.0 M S,?,H130,Cl (Ref. E86) 

daphnid 48-h LC50 = 1.32 M Cl (Ref. B&S74) 

daphnid 48-h LC50 = 1.11 M S,N,H45,Cl (Ref. B&C72) 

WQ 2E acute value = 0.195 P (Ref. S96) 

green algal 7-d EC50 = 0.160 M S,? NO3,Cl,SO4 (Ref. St81) 

RTELS 28-d LC50 = 0.470 M SR12h,?,H104,NO3 (Ref. B78) 

fish ChEC20 = 0.810 M (Ref. S96) 

fish Chronic Value (ChV) = 0.290 M S96 

fish ACR = 170.0 P 

daphnid ChEC20 = 0.004 M (Ref. S96) 

daphnid ChV = 0.010 M S,N,H45,Cl (Ref. B&C72) 

daphnid ChV = 0.005 M (Ref. S96) 

daphnid ACR = 110.0 P (Ref. B&C72) 

WQ 2E chronic value = 0.003 P (Ref. S96) 

algal ChV = 0.040 P EC50)ChV=4 

Abbreviations: 

ACR = acute-to-chronic ratio; 

Ch = chronic; 

ChV = chronic value; 

CC = concern concentration; 

ELS = early life stage; 

FHM = fathead minnow; 

H = hardness as CaCO3; 

N = nominal concentrations; 

? = method unknown; 

RT = rainbow trout; 

S = static method; 
53 

SR12h = static renewal method with renewals every 12 hours; and 

WQ = water quality value. 

Predictions were based on SARs for inorganic Co compounds; pH 7; hardness <180.0 mg/L as 

CaCO3; 100% active ingredients; mean measured concentrations of Co; and total organic carbon 

(TOC) <2.0 mg/L. 

Environmental concerns for Co compounds: 

moderate concern for acute toxicity to fish; 

moderate concern for acute toxicity to daphnids; 

high concern for toxicity to green algae; 

moderate concern for chronic toxicity to fish; 

high concern for chronic toxicity to daphnids; 

high concern for toxicity to green algae; 

assessment factor (AsF) = 10.0 

COC for fish = 0.030 

COC for daphnids = 0.001 

COC for green algae = 0.004 

The aquatic toxicity for the chelates and esters of Co are expected to be less than predicted using 

toxicity data based on the soluble ion and with a MW adjustment. 

The aquatic toxicity for organoCo could be higher than predicted using toxicity data based on the 

soluble ion and with a MW adjustment because the organic portion could enhance uptake in 

aquatic organisms. It is assumed that (1) the MWs of organoCo compounds would have to be 

less than 1000 daltons and (2) the log Kow of any organoCo would have to be less than 8.0 for 

toxicity to aquatic organisms to occur. It is also assumed that the aquatic toxicity of organoCo 

compounds will increase with increasing Kow when the log Kow <8.0. 

The major environmental toxicity concerns for this category are for chronic toxicity towards 

daphnids and toxicity towards green algae. The acute-to-chronic ratios of Co towards fish and 

daphnids are both greater than 100. The SAR method for Co compounds is the nearest 

analog(s) method. 

Boundaries. Cobalt compounds must have water solubilities equal to or greater than 1.0 μg/L 

(ppb) and molecular weights generally need to be near or below 1000. The log Kow of 

organoCo compounds has to be <8.0. 
54 

General Testing Strategy: 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (AI) 

and mean measured concentrations; measured TOC of dilution water in the control; ideally, 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; and solvent can be used to assist the test chemical to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the test 

chemical beyond its aqueous solubility limit. Stock solutions in water should be adjusted to pH 

near 7.0. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; ideally, 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; and solvent can be used to assist the test chemical to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the test 

chemical beyond its aqueous solubility limit. Stock solutions in water should be adjusted to pH 

near 7.0. 

If there is no significant risk from the test chemical after the results of the environmental base set 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. For organoCo compounds, or chelates or esters of Co, aerobic biodegradability 

according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the test chemical after the results of biodegradation testing 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 
55 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; 

measured TOC of dilution water in the control; ideally, mean measured concentrations in the 

highest treatment concentration should be equal the aqueous solubility limit; solvent can be used 

to assist the test chemical to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the test chemical beyond its aqueous solubility limit; 

and the 7-d ELS stage toxicity test cannot be substituted for the 28-d ELS toxicity test because 

the 7-d ELS toxicity test may underestimate chronic toxicity measured by the 28-d ELS toxicity 

test when the Chronic Values are compared. Stock solutions in water should be adjusted to pH 

near 7.0. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; ideally, mean measured 

concentrations in the highest treatment concentration should be equal the aqueous solubility 

limit; solvent can be used to assist the test chemical to reach its aqueous solubility limit quicker, 

but cannot be used to artificially enhance the water solubility of the test chemical beyond its 

aqueous solubility limit; and the 7-d daphnid chronic toxicity test cannot be substituted for the 

21-d toxicity test because the fish 7-d ELS toxicity test may underestimate chronic toxicity 

measured by the fish 28-d ELS toxicity test when the chronic values are compared. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seeding growth test, the earthworm toxicity test and the soil microbial community 

bioassay) will be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial 

organisms include: the plant whole life cycle test, the plant uptake test, and the soil microbial 

community bioassay. 

References.

B78 = Birge. 1978. USDOE Tech Info 

B&C72 = Biesinger&Christensen. 1972. J Fish Res Brd Can 29:1691 

B&S74 = Baudouin&Scoppa. 1974. Bull Environ Contam Toxicol 12:745 

E86 = Ewell etal. 1986. Environ Toxicol Chem 5:831 

S96 = Suter, GW. 1996. Environ Toxicol Chem 15:1234 

St81 = Stokes. 1981. J Plant Nutrit 3:667 

September, 1996; revised June 2010. 
56 

Category: Diazoniums Environmental Toxicity 

This category includes only aromatic diazoniums (N/N+

). Aliphatic diazoniums are very 

explosive and are only used as synthesizing agents. Aromatic diazoniums are used as 

fungicides on seeds and in soil, e.g., Fenaminosulf. It is known that diazoniums need to be 

absorbed to be toxic. Test data submitted to the Agency in the New Chemicals Program 

showed that diazo compounds with an average molecular weight (MWn) > 1000 have no effects 

at saturation to fish in the acute toxicity test. Therefore, compounds with MWn's > 1000 will be 

excluded from this category regardless of water solubility. In the NEAT state, diazoniums are 

solids, i.e., salts, and are most are soluble in aqueous media. Acute toxicity for diazoniums is 

assumed to be limited by the octanol/water partition coefficient (Kow) and MW. Above a log 

Kow value of 8.0 and/or MW >1000, diazoniums are not expected to be toxic at saturation during 

96-h exposures. Diazoniums are expected to be similar to anilines with respect to their Kow

cutoff value for acute toxicity. The acute toxicity of anilines diminishes at about a log Kow = 

7.0 (Veith and Broderius 1987). There are no known Kow limits for chronic toxicity at this time, 

but it may not be much above a log Kow = 10.0 for diazoniums. 

Hazard Concerns. Only the acute toxicity to fish for diazoniums has been determined by EPA 

through SAR Analysis using ECOSAR – a hazard estimation tool that uses chemical structure 

descriptors to estimate the acute and chronic toxicity of a substance to aquatic organisms. [Link 

for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. Daphnids are 

assumed to have similar sensitivity to fish, but green algae are expected to be more sensitive 

based on the use of diazoniums as fungicides. 

Environmental Fate: Diazonium fungicides, e.g., Fenaminosulf, are sensitive to light but are 

stabilized with Na sulphite. Fenaminosulf is stable in alkaline media. Diazoniums are also 

used in photography, e.g., diazo reproduction paper and film. Therefore, diazoniums are 

expected to be subject to rapid direct and indirect photolysis under environmentally realistic 

conditions. Diazoniums are also expected to slowly hydrolyze to phenols. 

Boundaries.: There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW. Acute toxicity expected with log Kow < 8.0 with a missing fragment for N/N+

.; 

no effects at saturation during 96-h exposures when log Kow ≥ 8.0. Chronic toxicity has no 

known upper bound for log Kow, but it is probably near 10.0 with a missing fragment for N/N+. 

MW must be < 1000. The environmental base set of tests will be requested for aquatic releases 

and the terrestrial base set of tests will be recommended for terrestrial exposures. When the log 

Kow is ≥ 10.0, chronic toxicity testing with fish and daphnids will be recommended.
57 

General Testing Strategy. 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. Since diazoniums compounds are photosensitive to uv light, it is best to avoid the use 

of fluorescent lights in toxicity tests. If they are used, then glass filters should be used. The 

acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids (Harmonized 

Test Guideline 850.1010) will be done using the flow-through method with measured 

concentrations; effective concentrations will be based on 100% active ingredients (AI) and mean 

measured concentrations; measured TOC of dilution water in the control; the highest treatment 

concentration on a nominal-basis should not exceed the aqueous solubility limit; and solvent can 

be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the 

highest treatment concentration on a nominal-basis cannot exceed the PMN's aqueous solubility 

limit; and solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but 

cannot be used to artificially enhance the water solubility of the PMN beyond its aqueous 

solubility limit. 

If there is no significant risk from the PMN after the results of the environmental base set have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water— Indirect Photolysis Screening Test 

(Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, go to Tier 

4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 
58 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then prepare 

a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. For example, the most 

sensitive species from the environmental base set has an EC50 value = 2.0 mg/L (based on 100% 

active ingredients [AI]), therefore, prepare a 5.0 mg/L stock solution based on 100% AI using 

the standard humic-containing solution. This stock solution is exposed to sunlight for at least 6 

half-lives to ensure that all of the PMN has been photolyzed, and then this stock solution is used 

to retest the most sensitive aquatic species to determine if the photolysis products of the PMN 

are more or less toxic that the PMN. 

Tier 4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured 

TOC of dilution water in the control; the highest treatment concentration on a nominal-basis 

should not exceed the aqueous solubility limit of the PMN; solvent can be used to assist the 

PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the 

water solubility of the PMN beyond its aqueous solubility limit; and the 7-d ELS stage toxicity 

test cannot be substituted for the 28-d ELS toxicity test because Van Leeuwen et al (1990) have 

demonstrated that the 7-d ELS toxicity test underestimated the chronic toxicity of anilines 

measured by the 28-d ELS toxicity test by >5.3 times when the NOECs were compared (see 

Table VII in Van Leeuwen). 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; the highest treatment concentration 

on a nominal-basis should be set at the aqueous solubility limit; solvent can be used to assist the 

PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the 

water solubility of the PMN beyond its aqueous solubility limit; and the 7-d daphnid chronic 

toxicity test cannot be substituted for the 21-d toxicity test because Van Leeuwen et al (1990) 

have demonstrated that the fish 7-d ELS toxicity test underestimated the chronic toxicity of 

anilines measured by the fish 28-d ELS toxicity test by >5.3 times when the NOECs were 

compared (see Table VII in Van Leeuwen). 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 
59 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200], the avian acute oral toxicity test 

[Harmonized Test Guideline 850.2100], and the soil microbial community bioassay [Harmonized 

Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic toxicity 

testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), avian 

reproduction toxicity test (Harmonized Test Guideline 850.2300), and the soil microbial 

community bioassay (Harmonized Test Guideline 850.5100).

References.

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

Veith GD and Broderius SJ. 1987. Structure-toxicity relationships for industrial chemicals 

causing type (II) narcosis syndrome. In Kaiser KLE (ed), QSAR In Environmental Toxicology 

-II, pp. 385-391. Reidel Publishing Company. 

November, 1991; revised June 2010 
60 

Category: Dichlorobenzidine-based Pigments Human Health 

Environmental Toxicity 

Other Names: Diarylide Pigments, DCB Pigments, Pigment Yellows 

Definition: Any diazo pigment containing the substructure, dichlorobenzidine, and coupled 

with acetoacetanilide. 

Hazard Concerns. There are oncogenicity/mutagenicity concerns for dichlorobenzidine-based 

pigments based on the potential release of 3,3'-dichlorobenzidine and on the presence of residual 

(unbound) dichlorobenzidine. DCB is a known animal carcinogen and a suspect human 

carcinogen. In addition, DCB is known to bioconcentrate in the tissues of aquatic organisms. 

Boundaries. Concern for the intact pigment is restricted to uses at temperatures exceeding 

200oC. Data submitted to the Agency under TSCA section 8(e) show that DCB pigments break 

down to release DCB as a vapor from colored polymers when heated to extrusion temperatures 

(> 200oC) and, from sheetmetal coatings during curing. Though little information exists on the 

biodegradation of pigments in sediments, data on other low water soluble colorants, indicate that 

biodegradation may occur over a period of months, possibly resulting in the release of DCB. 

General Testing Strategy. 

EPA's New Chemicals Program considers the following tests to be appropriate to address the 

potential for DCB pigments to pose a significant risk to health or the environment: 

1. Monitoring data to detect the presence of DCB under actual conditions of use; temperature, 

dwell time, % pigment in polymer or coating, and type of polymer or coating. 

2. If there are releases to water, an anaerobic biodegradation assay. 

References:
61 

Appleton HT, Sikka HC. 1980. Accumulation, elimination, and metabolism of 

3,3'-dichlorobenzidine in the bluegill sunfish. Environ Sci Technol 14:50-54. 

Pliss GB. 1963. On some regular relationship between carcinogenicity of aminobiphenyl 

derivatives and the structure of the substance. Acta Unio Int Cancrum 19:499-501. 

Stula EF, Sherman H, Reinhardt CF. 1975. Experimental neoplasia in rats from oral 

administration of 3,3'-dichlorobenzidine, 4,4'-methylene-bis(2-chloroaniline), and 

4,4'-methylene-bis(2-methylaniline). Toxicol Appl Pharmacol 32:159-176. 

Stula EF, Barnes JR, Sherman H. 1978. Liver and urinary bladder tumors in dogs from 

3,3-dichlorobenzidine. 1978. J Environ Pathol Toxicol 1:475-490. 

TSCA Section 8(e) Documents: 

8EHQ-0490-0962 INIT 

8EHQ-0590-0962 SUPPL 

8EHQ-0690-0962 FLWP 

8EHQ-0790-0962 SUPPL 

8EHQ-0890-0962 SUPPL 

March, 1994 
62 

Category: Dithiocarbamates Environmental Toxicity 

Definition. This category includes N,N-dialkyldithiocarbamates (DDC); 

ethylenebisdithiocarbamates (BDC); and their metal salts which include but are not limited to 

zinc, sodium, iron, manganese, copper, lead, mercury, silver and selenium. The alkyl groups of 

the DDCs generally include, methyl through butyl, but may be larger. This category also 

includes the degradation products of DDC and BDC which may include disulfide moieties, 

sulfide moieties, thiourea moieties, urea moieties, polymeric sulfide moieties, 

dithizaole-3-thiones, cyclic thioureas and cyclic ureas as indicated in the generic environmental 

hazard assessment. 

Hazard Concerns: Many members of this category are commercial insecticides, fungicides, 

disinfectants, rodenticides, antioxidants, slimicides, algalicides, bactericides and heavy metal 

chelators. Their mode of toxic action apparently results from interference with 

metallo-enzymes in living cells; the toxicity has been attributed to either DDCs and BDCs or 

their degradation products. All of the known dithiocarbamates are acutely toxic to fish, algae 

and bacteria at < 10 mg/L, and to aquatic invertebrates at < 1 mg/L. Chronic toxicity to fish 

and aquatic invertebrates ranges from 0.001 to 2 mg/L and 0.011 to 0.111 mg/L, respectively. 

In general, the SARs for the dithiocarbamates and their degradation products are sigmoidal with 

acute and chronic toxicity increasing with increasing Kow. The sigmoidal relationship between 

Kow and toxicity of the dithiocarbamates is very poor statistically. Consequently, toxicity 

predictions will be made using either the closest analog or averaging data for the two closest 

analogs which bracket the dithiocarbamate under question. The SAR for the degradation 

products is much more robust and a series of SARs will be used to predict acute toxicity of 

degradation products toward fish, daphnids and Photobacterim phosphoreum; and chronic 

toxicity toward fish, daphnids and green algae. 

Boundaries. There are no known lower boundaries. The upper boundaries are based on Kow

and MW. When the log Kow value is < 5, the environmental base set of tests will be requested 

for aquatic releases and the terrestrial base set of tests will be recommended for terrestrial 

exposures. When the log Kow is between 5 and < 19, only chronic toxicity testing will be 

recommended. When the log Kow is > 19, no testing will be requested because no toxic effects 

at saturation will be expected. Generally, members of this category will have MWs of less than 

1000. 
63 

General Testing Strategy 

Tier 1. The acute aquatic base set of environmental toxicity tests will be recommended for 

aquatic exposures and the terrestrial base set of environmental toxicity tests (i.e., the early 

seeding growth test, the earthworm acute toxicity test and the soil microbial community 

bioassay) will be recommended for terrestrial exposures. 

Tier 2. If acute toxicity testing indicates a significant risk, then chronic toxicity with fish and 

aquatic invertebrates will be recommended as well as aerobic biodegradation testing. 

 Aerobic biodegradability can be determined using either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

August 1989; revised November 1995; revised June 2010 
64 

Category: Epoxides Human Health 

Environmental Toxicity 

Definition. Any molecular structure containing one or more epoxy groups is considered to be a 

member of the category: 

 O 

 /|

 -C-C- 

 | | 

Hazard Concerns.

Human Health: concerns for epoxides are for cancer and reproductive effects based on data for 

several analogous chemicals. There is greater concern for primary epoxides, than for epoxides 

with substitutions on both of the epoxy carbons 

Environmental Toxicity: is a function of the octanol-water partition coefficient. Compounds 

with log Kow 's >5 act as neutral organics producing simple narcosis, but at lower log Kow 's, 

epoxides display toxicity greater than that predicted for simple narcotics. The aquatic toxicity for 

epoxides and polyepoxides has been determined through SAR analysis by EPA using ECOSAR 

– a hazard estimation tool that uses chemical structure descriptors to estimate the acute and 

chronic toxicity of a substance to aquatic organisms. [Link for ECOSAR: 

http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

Boundaries. Structures with epoxy equivalent weights of >1,000 are presumed not to pose a 

hazard under any conditions. Concerns are confined to those species with molecular weights 

<1,000. Health concerns are restricted to species with molecular weights <500 if exposure is 

limited to the dermal route. 

Testing. To address health concerns the following tests are usually recommended for members 

of this class: (1) a lifetime cancer bioassay by the expected route of exposure, and (2) a 90-day 

subchronic with attention to pathology of the reproductive organs. To address ecotoxicity 

concerns, base set acute aquatic toxicity testing (algae: static method, daphnid and fish: 

flow-through method, all measured concentrations). 

September, 1988; revised June 2010 
65 

Category: Esters Environmental Toxicity 

Definition. This category includes all esters, polyesters, vinyl esters, allylic esters, propargylic 

esters, aliphatic esters, aromatic esters, carboxylic acid esters, and sulfonate esters. These 

compounds need to be absorbed to be toxic; therefore, compounds with MWs > 1000 will be 

excluded from this category. Acute toxicity for esters which are liquids at room temperature is 

known to be limited by the octanol/water partition coefficient (Kow). Above a log Kow value of 

≥ 5.0, esters show no effects at saturation during 96-h exposures (Veith et al 1984). Esters 

which are solids at room temperature may show no toxicity at saturation at lower Kow values 

depending on the melting point, i.e., the higher the melting point at a given Kow, the greater the 

likelihood that no acute toxicity will be observed at saturation. For solids, the 

no-effects-at-saturation point has to be determined on a case-by-case basis. The Kow limit for 

chronic toxicity is set at a log Kow = 8 for liquid esters. For solid esters, chronic toxicity testing 

will determine this Kow limit. 

Hazard Concerns. The toxicity for simple esters has been determined through SAR Analysis 

(Clements 1988). Esters are known to be more toxic than neutral organic chemicals, and this 

excess toxicity decreases with increasing Kow. The toxicity for vinyl esters, allylic esters, and 

propargylic esters is expected to be greater than for simple esters. Again, the additional excess 

toxicity of these vinyl esters, allylic esters, and propargylic esters is expected to decrease with 

increasing Kow. 

Members of this category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high 

toxicity (i.e., < 1 mg/L) depending on their Kow, MW, and melting point. 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW. Acute toxicity is expected when log Kow < 5.0; no effects at saturation during 

96-h exposures when log Kow > 5.0. The upper boundary for chronic toxicity is 8.0. MW will 

be < 1000. The environmental base set of tests will be requested for aquatic releases and the 

terrestrial base set of tests will be recommended for terrestrial exposures. When the log Kow is 

> 5.0, chronic toxicity testing with fish and daphnids will be recommended. 

Fate: Esters are subject to both abiotic and biotic hydrolysis, i.e., ester hydrolysis, and aerobic 

biodegradation. Aerobic biodegradation is expected to be the dominant route of transformation 

in the environment. 

General Testing Strategy. 

Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (AI) 

and mean measured concentrations; the highest treatment concentration on a nominal-basis 
66 

should not exceed the aqueous solubility limit; and solvent can be used to assist the ester to reach 

its aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility 

of the ester beyond its aqueous solubility limit. 

The algal toxicity test (Harmonized Test Guideline 850.5400) should be done with the static 

method; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the 

highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit of the ester; and solvent can be used to assist the ester to reach its aqueous solubility limit 

quicker, but cannot be used to artificially enhance the water solubility of the ester beyond its 

aqueous solubility limit. 

If there is no significant risk from the ester after the results of the environmental base set have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 2. 

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the ester after the results of the aerobic biodegradation testing 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; the 

highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit of the tested chemical; solvent can be used to assist the ester to reach its aqueous solubility 

limit quicker, but cannot be used to artificially enhance the water solubility of the ester beyond 

its aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be substituted for the 28-d 

ELS toxicity test because Van Leeuwen et al (1990) have demonstrated that the 7-d ELS toxicity 

test underestimated the chronic toxicity of anilines measured by the 28-d ELS toxicity test by 

>5.3 times when the NOECs were compared (see Table VII in Van Leeuwen). Both anilines 

and esters are more toxic than predicted based on narcosis alone, i.e., both esters and anilines 

have excess toxicity due to a more specific mode(s) of toxic action. A seven day exposure may 

not allow enough time for this excess toxicity to be expressed either because of not enough 

exposure and/or not enough time for metabolic activation. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 
67 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; the highest treatment concentration on a nominal-basis should not exceed the 

aqueous solubility limit of the ester; solvent can be used to assist the ester to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the ester 

above its aqueous solubility limit; and the 7-d daphnid chronic toxicity test cannot be substituted 

for the 21-d toxicity test (Van Leeuwen et al 1990). 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200], the avian acute oral toxicity test 

[Harmonized Test Guideline 850.2100], and the soil microbial community bioassay [Harmonized 

Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic toxicity 

testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), avian 

reproduction toxicity test (Harmonized Test Guideline 850.2300), and the soil microbial 

community bioassay (Harmonized Test Guideline 850.5100). 

References.

Clements, RG (editor). 1988. Estimating toxicity of industrial chemicals to aquatic organisms 

using structure-activity relationships. EPA-560-6-88-001. Washington, DC: Environmental 

Effects Branch, Health and Environmental Review Division, Office of Toxic Substances 

(TS-796), United States Environmental Protection Agency. Available from the National 

Technical Information Service, Springfield, VA 22161, PB89-117592. 

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

Veith GD, DeFoe D, and Knuth M. 1984. Structure-activity relationships for screening 

organic chemicals for potential ecotoxicity effects. Drug Metabolism Reviews 

15(7):1295-1003. 

November, 1991; revised June 2010 
68 

Category: Ethylene Glycol Ethers Human Health 

Definition. The ethylene glycol ether category is defined as follows: 

R-(OCH2CH2)n-OR' 

n = 1, 2, or 3 

R = alkyl C7 or less or phenyl or alkyl substituted phenyl 

R' = H or alkyl C7 or less or any group that can be chemically or 

metabolically removed to yield a glycol ether 

Hazard Concerns. Short-chain ethylene glycol ethers are absorbed by all routes of exposure 

and have caused irritation of skin, eyes, and mucous membranes; hemolysis, bone-marrow 

damage, and leukopenia of both lymphocytes and granulocytes; direct and indirect kidney 

damage; liver damage, immunotoxicity, and central nervous system (CNS) depression. 

Short-chain ethylene glycol ethers are also developmental and reproductive toxicants. 

2-Phenoxyethanol is known to cause hemolysis and eye irritation. 

Boundaries. There is evidence that developmental toxicity is reduced going from the methyl to 

the butyl ether, and that it is reduced going from the ethylene glycol to the triethylene glycol. 

However, there is still a concern for maternal toxicity as reflected in developmental and 

subchronic toxicity studies. The systemic toxicity of longer-chain glycol ethers and 

alkylphenyl glycol ethers is uncertain because data are not available. The alkyl chain length of 

C7 or less was chosen as a boundary for short-chain ethylene glycol ethers based on the available 

data. 

General Testing Strategy 

The New Chemicals Program considers the following tests to be the most appropriate for 

ethylene glycol ethers with sufficient exposure to potentially pose an unreasonable risk: 

Tier 1. Combined Repeated Dose Toxicity Study with the Reproduction/Developmental 

Toxicity Screen Test (OECD Guideline 422). If signs of hematuria are seen, red and white 

blood cell counts should be taken 2 days later except for female animals during pregnancy and 

lactation. 
69 

Tier 2. The need for further testing would be determined by the results of Tier 1. This could 

include any of the following tests. 

- Prenatal Developmental Toxicity via the most appropriate route (Harmonized Test 

Guideline 870.3700) 

- 2-Generation Reproduction Study via the most appropriate route (Harmonized Test 

Guideline 3800) 

- 90-Day Subchronic Study via the most appropriate route (Harmonized Test Guideline 

870.3465 – inhalation route; 870.3250 - dermal route; 870.3150 - oral route) 

- Immunotoxicity Study via the most appropriate route (Harmonized Test Guideline 

870.7800) 

June 1992, revised December 1997 
70 

Category: Hydrazines and Related Compounds Human Health 

Environmental Toxicity 

Definition: Any structure containing one or more of the following groups is considered to be 

a member of the category: 

Hazard Concerns: Concerns for carcinogenicity and chronic effects to liver, kidney, and 

blood are based on data for a number of hydrazines and related chemicals. In humans, 

hydrazine, itself, may affect the central nervous system, liver, and kidneys. The toxic effects of 

hydrazine exposure to humans may range from mild skin and eye irritation, and skin 

sensitization, to severe irritation and burns, pulmonary edema, CNS depression, as well as liver 

and kidney damage, which can lead to death. Hydrazine may also present a serious hazard to 

plant life and aquatic organisms. Ecotoxicity concerns are based on structure activity 

relationships (SAR) using data for a number of hydrazines and hydrazides. Hydrazine itself, 

(N2H4), is known to be acutely toxic to aquatic organisms at low levels, algae at < 100 ppb, 200 

ppb for fish, and 30 ppb for daphnids. 

Boundaries: There are no established boundaries for this category. The "typical" new 

chemical member of the category is a discrete (class I) chemical with a molecular weight <500. 

There is a greater concern for chemicals with few substitutions on the functional group than for 
71 

those with multiple substitutions. 

General Testing Strategy 

EPA considers the following tests to be appropriate to address health and ecotoxicity concerns: 

- Lifetime cancer bioassay by the expected route of exposure in two species of rodents 

(Harmonized Test Guideline 870.4200). 

- 90-Day subchronic in one species of rodent by the expected route of exposure to assess 

effects to the liver, kidney, and blood (Harmonized Test Guideline 870.3100). 

- Base-set ecotoxicity testing to include fish (Harmonized Test Guideline 850.1075) 

using the flow-through method, daphnids (Harmonized Test Guideline 850.1010) using 

the flow-through method and algae (Harmonized Test Guideline 850.5400) using the 

static method, all measured concentrations. 

Results of the acute ecotoxicity testing may trigger chronic fish (Harmonized Test Guideline 

850.1400) and daphnid (Harmonized Test Guideline 850.1010) testing. 

Environmental fate testing including, as appropriate, melting point (Harmonized Test Guideline 

830.7200) or boiling point (Harmonized Test Guideline 830.7220), water solubility (Harmonized 

Test Guideline 830.7840 or 830.7860), log Kow (Harmonized Test Guideline 830.7550, 830.7560 

or 830.7570; or OECD 123, Partition Coefficient (1-Octanol/Water): Slow-Stirring Method), 

vapor pressure (Harmonized Test Guideline 830.7950) and hydrolysis (Harmonized Test 

Guideline 830.2120). 

For aromatic hydrazines and related compounds, the following additional testing is 

recommended: 

- Phototransformation of Chemicals in Water—Direct Photolysis (OECD 316) or Indirect 

Photolysis Screening Test (Harmonized Test Guideline 835.5270) 

- Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test 

Guideline 835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized 

Test Guideline 835.3140) 

References.

1. Bhide, S.V., R.A. D'Souza, M.M. Sawai, & K.J. Ranadive (1976). International Journal 

of Cancer 18: 530. 
72 

2. Biancifiori, C (1970). Journal of the National Cancer Institute 44: 943. 

3. Biancifiori, C (1971). Lav. 1st Anat. Istol. Pat., Univ. Studi Perugia 31: 5. 

4. Biancifiori, C., E. Bucciarelli, D.B. Clayson, & F.E. Santilli (1964). British Journal of 

Cancer 18: 543. 

5. Hydrazine-RM2 Exit Document. OPPT Office Director's Meeting, Monday, December 

13, 1993. 

6. Juhasz, J., J. Balo, & B. Szende (1966). Nature (London) 210: 1377. 

7. Juhasz, J., J. Balo, & B. Szende (1967). Z. Krebsforsch 70: 150. 

8. Toth, B. (1969). Journal of the National Cancer Institute 42: 469. 

9. Toth, B. (1972). International Journal of Cancer 9: 109. 

September, 1988; revised June, 1994, revised October 1995; revised June 2010. 
73 

Category: Hindered Amines Human Health 

Definition. The category is at present not well defined. A "typical" new chemical hindered 

amine of concern has two or more hindered amine functional groups, usually the 

2,2,6,6-tetramethyl-4-piperidinyl group, and is used as a UV light stabilizer. 

Hazard Concerns. Health concerns for the category are based on data submitted to the 

Agency under '8(e) of TSCA for Tinuvin 144 and Chimassorb 944. The data indicate that 

these hindered amines, and presumably hindered amines similar in structure, are toxic to the 

immune system, liver, blood, the male reproductive system, and the G.I. tract. 

Boundaries. The boundaries of the category are not well defined. Tinuvin 144 has a 

molecular weight of 685, whereas Chimassorb 944 is a polymer with a number average 

molecular weight well in excess of 1,000. As a consequence, there is at present no molecular 

weight cutoff for hindered amines of concern to the new chemical program. 

It is assumed that there is little or no dermal absorption of problematic hindered amines because 

of their high molecular weights. Consequently, hindered amines in the new chemical program 

are only of concern if there is significant inhalation exposure associated with their manufacture, 

processing, or use. 

General Testing Strategy 

For hindered amines found to pose a potentially unreasonable risk, a 90-day oral subchronic test 

in rats is the recommended test. We have requested that emphasis be placed on hematology, 

the immune system, and on the male reproductive system. 

June 1990; revised March 1995 
74 

Category: Imides Environmental Toxicity 

Definition. This category includes all imides and maleimides. Substitutions may be aliphatic, 

aromatic, and/or halogens. The mode of toxic action of imides is unknown, but halogenated 

imides are used as microbial pesticides, specifically, fungicides, bactericides, slimicides, and 

algicides. It is assumed that these compounds need to be absorbed to be toxic; therefore, 

compounds with MWs > 1000 will be excluded from this category. Acute toxicity for imides 

which are liquids at room temperature is assumed to be limited by the octanol/water partition 

coefficient (Kow), and the limiting Kow value for acute toxicity is assumed to be about 5.0. The 

limiting value for chronic toxicity is assumed to be about 8.0. Imides which are solids at room 

temperature may show no toxicity at saturation at log Kow values < 5.0 depending on the melting 

point, i.e., the higher the melting point at a given Kow, the greater the likelihood that no toxicity 

will be observed at saturation. For solids, the no-effects-at-saturation determination has to be 

made on a case-by-case basis. 

Hazard Concerns. The acute toxicity for imides and maleimides have been determined 

through SAR Analysis by EPA using ECOSAR – a hazard estimation tool that uses chemical 

structure descriptors to estimate the acute and chronic toxicity of a substance to aquatic 

organisms. [Link for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

The acute toxicity of imides towards daphnids is expected to be similar to that of fish, but their 

toxicity towards green algae is expected to be greater because of their use as microbial 

pesticides. 

Polyimides may be more toxic than predicted using the general imide SAR. 

The toxicity of imides towards aquatic organisms can range from low (i.e., > 100.0 mg/L) to 

high toxicity (i.e., < 1.0 mg/L) depending on their Kow and MW. The higher the Kow and the 

lower the MW, the higher the toxicity (or the lower the EC50 value). 

Boundaries. There are no known lower log Kow and MW boundaries. The upper boundaries 

for acute toxicity will be set at a log Kow < 5.0; chronic toxicity limits will be set at a log Kow <

8.0. MW will be < 1000 for stable compounds. The environmental base set of tests will be 

requested for aquatic releases and the terrestrial base set of tests will be recommended for 

terrestrial exposures. 

General Testing Strategy. 

The aquatic base set of environmental toxicity tests will be recommended for aquatic exposures. 

The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (AI) 

and mean measured concentrations; measured TOC of dilution water in the control; the highest 

treatment concentration on a nominal-basis should equal the aqueous solubility limit; and solvent 
75 

can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the 

highest treatment concentration on a nominal-basis equal to the aqueous solubility limit; and 

solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be 

used to artificially enhance the water solubility. 

Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing (Harmonized Test 

Guideline 850.1400), with flow-through methods; measured concentrations; effective 

concentrations based on 100% active ingredients (AI) and mean measured concentrations; 

statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured TOC of 

dilution water in the control; the highest treatment concentration on a nominal-basis should be 

set at the aqueous solubility limit; solvent can be used to assist the PMN to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility; and the 

7-d ELS stage toxicity test cannot be substituted for the 28-d ELS toxicity test because Van 

Leeuwen et al (1990) have demonstrated that the 7-d ELS toxicity test underestimated the 

chronic toxicity of anilines measured by the 28-d ELS toxicity test by >5.3 times when the 

NOECs were compared (see Table VII in Van Leeuwen); 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; the highest treatment concentration 

on a nominal-basis should be set at the aqueous solubility limit; solvent can be used to assist the 

PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the 

water solubility; and the 7-d daphnid chronic toxicity test cannot be substituted for the 21-d 

toxicity test because Van Leeuwen et al (1990) have demonstrated that the fish 7-d ELS toxicity 

test underestimated the chronic toxicity of anilines measured by the fish 28-d ELS toxicity test 

by >5.3 times when the NOECs were compared (see Table VII in Van Leeuwen). 

The terrestrial base set of environmental toxicity tests (i.e., the early seedling growth test 

(Harmonized Test Guideline 850.4230], the earthworm acute toxicity test (Harmonized Test 

Guideline 850.6200), and the soil microbial community bioassay (Harmonized Test Guideline 

850.5100) will be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial 

organisms include: the plant whole life cycle test (Harmonized Test Guideline 850.4150), the 

plant uptake test (Harmonized Test Guideline 850.4800), and the soil microbial community 

bioassay (Harmonized Test Guideline 850.5100).
76 

References.

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

April, 1991; revised June 2010 
77 

Category: Diisocyanates Human Health 

Definition. Any molecular structure containing two or more isocyanate groups is considered to 

be a member of the category for new chemical purposes: 

 R-(N=C=O)>2

Members of the class include new isocyanate monomers as well as new oligomers, polymers, 

prepolymers, or reaction products of existing isocyanate monomers. Most new chemical 

diisocyanates of concern are polymers or oligomers containing well-known diisocyanate 

monomers such as toluene diisocyanate (TDI) or 4,4'-methylenediphenyl diisocyanate (MDI). 

Hazard Concerns. Diisocyanates are of concern for potential dermal and respiratory 

sensitization, and for pulmonary toxicity. Based on conflicting animal and human data for 

respiratory sensitization, the Agency has determined that there is presently not a reliable animal 

model for testing diisocyanates for potential respiratory sensitization. At this time, it is 

assumed that all diisocyanates may be potential human respiratory sensitizers. 

Most members of the diisocyanate category have not been tested for carcinogenic potential. 

Though the aromatic diisocyanates [MDI, TDI, dianisidine diisocyanate (DADI)] tested positive 

and one aliphatic diisocyanate [hexamethylene diisocyanate (HDI)] tested negative in one 

species, it is premature to make any generalizations about the carcinogenic potential of aromatic 

versus aliphatic diisocyanates. 

Boundaries. Structures with an isocyanate equivalent weight of >5,000 are presumed not to 

pose a hazard under any conditions. Typically, concerns are confined to those species with 

molecular weights <1,000. 

Frequently, new chemical isocyanates are manufactured with a significant excess of isocyanate 

monomer. Under these circumstances, the excess monomer is usually regarded as more 

hazardous than the "new" chemical component, and these PMN substances are ordinarily not 

regulated under Section 5 of TSCA. For the purposes of risk assessment within the New 

Chemicals Program, a PMN substance is considered "existing" if more than 50% of the free 

isocyanate groups in the PMN substance (new chemical component + existing chemical 

monomer) reside on unreacted monomer(s). This does not relieve a Company, however, of any 

obligations to submit a PMN for the new chemical isocyanate if indeed it is not listed on the 

TSCA Inventory. 

General Testing Strategy. The following testing is recommended to address the potential for 

pulmonary toxicity and dermal sensitization. 

 
78 

- Dermal sensitization (Harmonized Test Guideline 870.2600). 

- 90-day Subchronic inhalation toxicity test in rodents (Harmonized Test Guideline 

870.3465). 

In addition, appropriate hazard communication needs to be developed and implemented. 

Health and Safety Information. The following information provides guidance in developing 

hazard communication and protective measures language to accompany new diisocyanate 

chemicals and formulations. It is based on the Agency’s current understanding of the hazards 

associated with diisocyanates and the most effective means to limit exposure. 

 

Warnings. Exposure to diisocyanates may cause the following human health 

effects: skin irritation and allergic reactions, respiratory irritation, respiratory 

sensitization, and lung toxicity; some diisocyanates also may cause cancer. The 

likelihood that these effects will occur depends on a number of factors; among 

them, the level of exposure, frequency of exposure, part of the body exposed, and 

sensitivity of the exposed individual. 

Symptoms of allergic reaction and respiratory sensitization include rashes, cough, shortness of 

breath, asthma, chest tightness and other breathing difficulties. There is uncertainty as to the 

mechanism by which sensitization occurs. In sensitized individuals, exposure to even small 

amounts of diisocyanates (below government-recommended workplace exposure levels) may 

cause allergic respiratory reactions like asthma and severe breathing difficulties. It is especially 

important to note that contact with skin may lead to respiratory sensitization or cause other 

allergic reactions. In some cases, the effects of diisocyanate exposure may be immediate and 

life-threatening; in others, the effects may be delayed and occur hours after the exposure has 

ended. Repeat or prolonged exposure to diisocyanates may also cause irritation to eyes, skin, 

respiratory tract and lungs, as well as adverse chronic lung effects, like decreased lung capacity 

and function. Individuals experiencing shortness of breath, tightness in the chest or other 

problems breathing should seek immediate medical attention. 

Protective Measures. In workplaces where individuals handle diisocyanates 

or coatings or other formulations that contain them, an industrial hygiene and 

safety program should be operative. Important components of this program 

include: hazard communication and training on safe handling practices; use of 

efficient and well-maintained application equipment, engineering controls and 

personal protective equipment; housekeeping procedures including spill 

prevention and cleanup practices; and, if feasible, means to measure airborne 

levels of polyisocyanates and diisocyanates. 

During spray applications, workers should take precautions to avoid breathing vapors, mists or 

aerosols. Inhalation exposures should be limited to <0.05 mg/m3

 as an 8-hour time-weighted 
79 

average (TWA) for combined polyisocyanates and diisocyanates.1

 Engineering controls should 

serve as the first, most effective means of reducing airborne polyisocyanate and diisocyanate 

concentrations; an appropriate NIOSH/MSHA-approved respirator should be used as a 

secondary tool to lower exposures. Currently, downdraft spray booths and high-volume 

low-pressure (HVLP) spray guns appear to offer the most efficient technology to reduce 

inhalation exposures; a maintenance program should always be used to ensure optimal operating 

efficiencies. To limit dermal contact, individuals should wear impermeable gloves, protective 

clothing and goggles or glasses with side shields. 

 

 

May 1990; revised July 1993, February 1995, and February, 1997 

 1

0.05 mg/m3 or 0.005 ppm TWA is the American Conference of Government Industrial 

Hygienists (ACGIH) Threshold Limit Value (TLV) for each hexamethylene diisocyanate 

(HMDI), toluene-2,4-diisocyanate (TDI), and methylene bisphenyl isocyanate (MDI). Also, 

OSHA has set 0.02 ppm as exposure ceilings for both TDI and MDI. 
80 

Category: β-Naphthylamines, Sulfonated Human Health 

Definition. Any new chemical whose structure is consistent with the following general 

structure is considered to be a member of the category of monosulfonated β-naphthylamines: 

Included in the category are azo dyes which release a sulfonated β-naphthylamine upon 

reduction of azo bonds. Also included in the category are N-acetylated sulfonated 

β-naphthylamines. 

Hazard Concerns. Based on analogy to β-naphthylamine per se, members of the class are 

considered potential carcinogens. A number of mono- and disulfonated β -naphthylamines are 

positive in the Ames assay, and some are active in the mouse lung adenoma assay. The 

presence of one or two sulfonate groups or the sulfatoethylsulfone group is likely to slow 

systemic uptake and enhance excretion, however, the extent of these mitigating effects is 

unknown. 

Boundaries. Concern is restricted to sulfonated β -naphthylamines where not more than two 

sulfonate or sulfatoethylsulfone group(s) are on the ring distal to the β -amino group. The 

Agency has sufficient data to indicate that β -naphthylamines where a sulfonate group is on the 

proximal ring are unlikely to be carcinogenic. 

General Testing Strategy. 

The New Chemicals Program considers the following tests to be the most appropriate for monoand di-sulfonated β-naphthylamines found to pose an unreasonable risk: 

- An Ames test or, for azo dyes, an Ames test with the Prival modification, and 

- An unscheduled DNA synthesis test in rat hepatocytes.. For azo dyes, it is necessary 

that the specific sulfonated -naphthylamine in question be isolated prior to testing. 
81 

For both tests, β -naphthylamine is to serve as an additional positive control. 

If the results of the genotoxicity testing indicate that the new chemical is genotoxic, a two- year, 

two-species cancer bioassay would be required. 

April 1991, updated June 1999 
82 

Category: Lanthanides or Rare Earth Metals Environmental Toxicity 

Definition. This category includes inorganic salts, complexes organic acids, and 

organometallic compounds or lanthanides or rare earth metals. There are 14 

naturally-occurring lanthanides or rare earth metals: 

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

Name Symbol MW CASRN 

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

Lanthanum La 139 [7439-91-0] 

Cerium Ce 140 [7440-45-1] 

Praseodymium Pr 141 [7440-10-0] 

Neodymium Nd 144 [7440-00-8] 

Samarium Sm 150 [7440-19-9] 

Europium Eu 152 [7440-53-1] 

Gadolinium Gd 157 [7440-54-2] 

Terbium Tb 159 [7440-27-9] 

Dysprosium Dy 163 [7429-91-6] 

Holmium Ho 165 [7440-60-0] 

Erbium Er 167 [7440-52-0] 

Thulium Tm 169 [7440-30-4] 

Ytterbium Yb 173 [7440-64-4] 

Lutetium Lu 175 [7439-94-3] 

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

The lanthanide rare earth metals are very similar to each other. Their most important oxidation 

state is +3 for all. None are known to be essential to biological species. Across the lanthanide 

series from La to Lu, there is a general or steady decrease in their (1) atomic radii, (2) covalent 

radii, and (3) radii of their tripositve ions due to the addition of electrons at the 4f electron shell. 

 This decrease in radii leads to a corresponding increase in the polarizing power of their ions 

and in the stability of complexes of their ions. They all have similar chemistry behaviors. 

Hazard Concerns. The only toxicity data available for the lanthanide series are for La 

[7439-91-0]. Soluble salts of La are known to have high chronic toxicity towards fish, 

moderate chronic toxicity towards green algae, and low acute toxicity towards daphnids based on 

exposures in moderately hard water and in terms of mg La/L. Toxicity information is only 

available for La trichloride [10099-58-8] and La triacetate [917-70-4]. The toxicity profile for 

La based on available toxicity data, i.e., measured (M) and predicted (P), mg La/L (ppm La), and 

moderate hardness (i.e., <180.0 mg/L as CaCO3) is: 
83 

fish 96-h LC50 < 1.0 Predicted, ACR10 

daphnid 48-h LC50 = 160.0 Measured, S, N, BK59 

green algal 96-h EC50 < 1.0 Predicted, ACR4 

fish chronic value(ChV) = 0.020 Measured, SR12, M H104, B78 

daphnid ChV = 20.0 Predicted, ACR10 

algal ChV = 0.150 Measured S,N,BK59 

The lanthanides are assumed to be more toxic in soft water than hard water based on data for 

other heavy metals. 

Boundaries. The toxicity of the lanthanide rare earth metals depends on their 

physico/chemical properties and the hardness of receiving waters. The toxicity of their salts 

and their complexes with organic acids are expected to be related to their water solubility, their 

MWs, and the stability of their complexes. The toxicities of lanthanide organometallic 

compounds, if they exist, are expected to be related to their octanol/water partition coefficient 

(Kow). 

The most important property determining the toxicity of chemicals derived from lanthanide rare 

earth metals is their water solubility. Water solubility cannot be estimated accurately and has to 

be measured. The water solubility of organometallic compounds is expected to decrease as 

Kow increases. There is no lower bound for Kow and the upper bound cannot be determined at 

this time since the Kow fragment-constant for any of the lanthanide rare earth metals are not 

known. In addition to solubility, MW is also an important boundary. Highly stable 

complexes and organometallics with MWs > 1000 are not expected to be absorbed by aquatic 

organisms even if they are water soluble. Therefore, only lanthanide rare earth 

metal-compounds with MWs < 1000 are expected to be toxic. 

General Testing Strategy. 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method; effective 

concentrations will be based on 100% active ingredients (ai) and mean measured concentrations; 

the total organic carbon (TOC) concentration of dilution water in the control must be less than 

2.0 mg TOC/L; TOC must be measured in the control just prior to the start of the test; the highest 

treatment concentration on a nominal-basis should not exceed the aqueous solubility limit of the 

tested compound; solvent can be used to assist the compound to reach its aqueous solubility limit 

quicker, but cannot be used to artificially enhance the water solubility of the compound beyond 

its aqueous solubility limit; and hardness of dilution water has to be less than 180.0 mg/L as 

CaCO3. If toxicity mitigation testing is done with humic acid, then the static method with 

nominal concentrations will be recommended. 
84 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with the static 

method; effective concentrations based on 100% ai and mean measured concentrations; 

statistical analysis of effective concentrations at 24, 48, 72, and 96 hours; test medium with no 

more than 0.300 mg/L EDTA as a final concentration; the TOC of the test/growth medium 

should be less than 2.0 mg TOC/L; TOC should be measured just prior to the start of the test; 

the highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit of the tested compound; and solvent can be used to assist the compound to reach its 

aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility of 

the compound beyond its aqueous solubility limit. If toxicity mitigation testing is done with 

humic acid, then nominal concentrations will be recommended. 

If there is no significant risk from the chemical after the results of the environmental base set 

have been integrated into the risk assessment, then no further testing will be recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with the flow-through method; effective concentrations 

based on 100% ai and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, 21, and 28; the TOC of dilution water in the control should be less 

than 2.0 mg TOC/L; TOC should be measured in the controls just prior to and during the test; 

the highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit of the tested compound; solvent can be used to assist the compound to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the 

compound beyond its aqueous solubility limit; and hardness of dilution water has to be less than 

180.0 mg/L as CaCO3. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with the flow-through 

method; effective concentrations based on 100% AI and mean measured concentrations; 

statistical analysis of effective concentrations at days 7, 14, and 21; the TOC of dilution water in 

the control should not exceed 2.0 mg TOC/L; TOC must be measured in the controls just prior to 

and during the test; the highest treatment concentration on a nominal-basis should not exceed the 

aqueous solubility limit of the tested compound; solvent can be used to assist the compound to 

reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the water 

solubility of the compound beyond its aqueous solubility limit; and hardness of dilution water 

has to be less than 180.0 mg/L as CaCO3. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

will be recommended for terrestrial exposures. The terrestrial base set includes: the early 

seeding growth test (Harmonized Test Guideline 850.4230), the earthworm toxicity test 

(Harmonized Test Guideline 850.6200), the soil microbial community bioassay (Harmonized 

Test Guideline 850.5100), and the avian acute oral toxicity test (Harmonized Test Guideline 

850.2100). Chronic toxicity testing for terrestrial organisms include: the plant whole life cycle 
85 

test (Harmonized Test Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 

850.4800), and the avian reproduction test (Harmonized Test Guideline 850.2300 for bobwhite 

quail or for mallard duck). 

February, 1998 
86 

Category: Neutral Organics Environmental Toxicity 

Definition. This broad category includes non-reactive non-ionizable organic chemicals such as 

alcohols, ketones, ethers, alkyl halides, aryl halides, and aromatic hydrocarbons. 

 

Hazard Concerns. Neutral organics are environmentally toxic because of their ability to 

produce simple narcosis in aquatic species. Toxicity is a function of the octanol-water partition 

coefficient. Compounds with log Kow values of <5 exhibit toxicity within 96 hours. At log 

Kow of 5-8, toxicity is apparent only after extended exposure. Compounds with a log Kow 

>8 are not toxic at water saturation even after prolonged exposure. There are a number of 

QSARs (quantitative structure-activity relationships) to predict the toxicity of neutral organics. 

Boundaries. Neutral organics of concern generally have MWs less than 1,000 and Log Kow 

values <8. QSAR predictions of toxicity are constrained by water solubility. If a predicted 

toxicity level exceeds water saturation, then a longer test is needed to observe toxicity. 

General Testing Strategy 

To address ecotoxicity concerns, base set acute aquatic toxicity testing (algae (Harmonized Test 

Guideline 850.5400): static method, daphnid (Harmonized Test Guideline 850.1010) and fish 

(Harmonized Test Guideline 850.1075): flow-through method, all measured concentrations). 
87 

To properly assess any human and environmental toxicity or exposure, certain 

environmental fate properties, such as aerobic biodegradation, need to be measured. 

Aerobic biodegradability can be determined using either of these two test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

The physical state and electronic charge of the PMN substance should also be reported. 

For some neutral organics (e.g. ketones), Direct Photolysis (OECD 316) or Indirect Photolysis 

Screening Test (Harmonized Test Guideline 835.5270) AND possibly biodegradation testing is 

recommended. 

For some neutral organics (e.g. alkyl halides) hydrolysis testing (Harmonized Test Guideline 

835.2120) AND possibly biodegradation testing is recommended. 

September 1988; revised October 1995; revised June 2010
88 

Category: Nickel Compounds Human Health 

Environmental Toxicity 

Definition. Inorganic and organic compounds of nickel in which there is the potential for 

uptake of either Ni2+ or organonickel. 

Hazard Concerns. Nickel compounds e.g., nickel refinery dust, and its major component 

nickel subsulfide, have been shown to be carcinogenic in humans. Some nickel compounds are 

known to be genotoxic. IRIS has established an oral RfD for the soluble salts of nickel of 2 x 

10-2 mg/kg/d (1992) based on effects on organ weights in a two-year feeding study in rats. In 

the study, there was a statistically significant reduction in total body weight, higher 

heart-to-body weight ratios and lower liver-to-body weight ratios than controls. In addition to 

the effects on organ weights found in the critical two-year study, two other sensitive endpoints 

exist, neonatal mortality and dermatotoxicity. While no reproductive effects have been 

associated with nickel exposure to humans, several studies in laboratory animals have 

demonstrated fetotoxicity. 

Soluble inorganic nickel compounds produce acute and chronic toxicity in freshwater and 

saltwater aquatic organisms over a wide range of concentrations but bioconcentrates only to a 

small degree. There are no known toxicity data for organonickel compounds. 

 

Boundaries. Any nickel compound that will release Ni2+ is considered hazardous. Conversely, 

there are no available data to suggest that nickel compounds in which the Ni2+ is not released 

may pose a health hazard. 

The boundaries for ecotoxicity of Ni2+ compounds depend on whether they are Ni2+ salts, Ni2+

chelates, or organonickel compounds. There is also a molecular weight boundary for strong ion 

pairs/complexes which is 1000. 

The boundaries for organonickel compounds (e.g., Kow of the organic portion) are undefined but 

the molecular weight boundary is expected to be 1000. 

Occupational Exposure Controls. Because nickel compounds have been shown to be toxic by 

the inhalation/ingestion route, exposure controls that maintain airborne exposures at 0.1 mg/m3

or below are needed (consistent with OSHA PEL TWA). In addition, since nickel compounds 

are also toxic by the dermal route, NIOSH approved protective gloves are also recommended. 

Testing. Depending upon estimated workplace exposures and releases to water, which will be 

assessed on a case-by-case basis, the following testing may be recommended: 

To address health effects concerns due to the toxicity of nickel and its compounds, the following 

tests may be recommended: 
89 

A 90-day subchronic study in rats by an appropriate route to assess systemic toxicity 

(Harmonized Test Guideline 870.3100 or 870.3250 or 870.3465) 

Results of the 90-day study may trigger a lifetime bioassay in rats and mice by the 

inhalation route to assess potential carcinogenicity (Harmonized Test Guideline 

870.4200) 

To address ecotoxicity concerns due to toxicity of nickel and its compounds, the following base 

set tests may be recommended: 

Acute fish toxicity test Harmonized Test Guideline 850.1075 

Acute daphnid toxicity test Harmonized Test Guideline 850.1010 

Green algae toxicity test Harmonized Test Guideline 850.5400 

All tests utilize measured concentrations. 

To properly assess human and environmental toxicity or exposure, certain physico-chemical or 

environmental fate properties need to be measured: 

Water solubility Harmonized Test Guideline 830.7840 or 

830.7860 

Octanol/water partition coefficient (Kow ) Harmonized Test Guideline 830.7550 or 

830.7560 or 830.7570; or OECD 123, 

Partition Coefficient (1-Octanol/Water): 

Slow-Stirring Method 

Vapor pressure Harmonized Test Guideline 830.7950 

Melting point-melting range Harmonized Test Guideline 830.7200 

Boiling point Harmonized Test Guideline 830.7220 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

References.

IRIS access. # 1271 (09/30/87) Nickel, soluble salts. 

OSHA PELs (1995-1996) 

September 1996; revised June 2010 
90 

Category: Nitriles, allylic/vinyl Environmental Toxicity

Definition. This category includes classes of organic compounds that have either a double 

bond (C=C) or triple bond (C≡C) in close proximity to a nitrile (C≡N) either next to or one 

carbon removed. The carbon-carbon unsaturation near the nitrile results in increased 

metabolical reactivity in organisms which, in turn, results in excess aquatic toxicity in addition 

to narcosis or baseline toxicity.

Compounds included in this category include but are not limited to allylic nitriles 

(R-C=CCC≡N), vinyl nitriles (R-C=CC≡N), and propargyl nitriles which include alpha-alknyl 

nitriles (R-C≡CC≡N), beta-alknyl nitriles (R-C≡CCC≡N), and gamma-alknyl nitriles 

(R-C≡CCCC≡N).

Toxicity Concern. The aquatic toxicity for allylic/vinyl nitriles have been determined by EPA 

through SAR Analysis using ECOSAR – a hazard estimation tool that uses chemical structure 

descriptors to estimate the acute and chronic toxicity of a substance to aquatic organisms. [Link 

for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. Propargyl nitriles 

are expected to have similar toxicity or greater toxicity. These chemicals are known to be more 

toxic than neutral organic chemicals, and this excess toxicity decreases with increasing Kow. 

Members of this category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high 

toxicity (i.e., < 1 mg/L) depending on their Kow, MW, and melting point.

Boundaries or Domain. There are no known lower boundaries. The upper boundaries will 

be based on Kow, MW, and melting point (mp). These compounds need to be absorbed to be 

toxic; therefore, compounds with MWs < 1000 are expected to cause toxicity, while compounds 

with MWs > 1000 are expected to have low toxicity to aquatic organisms. Likewise, if the 

effective cross-sectional diameter is greater than 1.5 nanometers, then absorption thru 

membranes is expected to be nil and low toxicity towards aquatic organisms is expected.

Acute toxicity for these chemicals which are liquids at room temperature is known to be limited 

by the octanol/water partition coefficient (Kow). Below a log Kow value of 5, these 

compounds are expected to show acute and chronic toxicity to aquatic organisms. Above a log 

Kow value of 5.0, these chemicals are expected to show low acute toxicity towards fish and 

aquatic invertebrates (daphnids), or no effects at saturation during 96-h exposures to fish and 

48-h exposures to daphnids. Above a log Kow of 6.4, these chemicals are expected to show 

low toxicity towards green algae in terms of inhibition of biomass, or no obtainable EC50 during 

72-h and 96-h exposures to green algae. 

Allylic/vinyl nitriles which are solids at room temperature may show no acute toxicity at 

saturation at lower Kow values depending on the melting point, i.e., the higher the melting point 

at a given Kow, the greater the likelihood that no acute toxicity will be observed at saturation. 

For solids, the no-effects-at-saturation point for acute toxicity has to be determined on a 

case-by-case basis by comparing the predicted LC50/EC50 to the predicted or measured water 
91 

solubility. 

These compounds should show only chronic toxicity towards fish and daphnids when log Kow 

values are greater than 5 and less than 8. For green algae, only chronic values should be 

measurable between log Kow values of 6.4 and 8. 

The Kow limit for chronic toxicity is set at a log Kow = 8 for liquid compounds. All allylic/vinyl 

nitriles should show no toxic effects to fish, daphnids, and green algae when the log Kow is 

greater than 8. For solids, chronic toxicity testing will allow determination of a Kow limit.

Environmental Fate: Aerobic biodegradation is expected to be the dominant route of 

transformation in the environment.

General Testing Strategy: I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (ai) 

and mean measured concentrations; dilution water hardness less than 150 mg/L as CaCO3; 

dilution water total organic carbon (TOC) less than 2.0 mg TOC/L; the highest treatment 

concentration on a nominal-basis should not exceed the aqueous solubility limit of the tested 

chemical; and solvent can be used to assist the chemical to reach its aqueous solubility limit 

quicker, but cannot be used to artificially enhance the water solubility of the chemical beyond its 

aqueous solubility limit. 

The algal toxicity test (Harmonized Test Guideline 850.5400) should be done with the static 

method; measured concentrations; effective concentrations based on 100% active ingredients (ai) 

and mean measured concentrations; statistical analysis of effective concentrations based on (1) 

cells/mL, (2) area under the growth curve, and (3) growth rate at 24, 48, 72, and 96 hours; test 

medium with at least 0.300 mg/L EDTA-Na salt as a final concentration; the highest treatment 

concentration on a nominal-basis should not exceed the aqueous solubility limit of the chemical; 

and solvent can be used to assist the chemical to reach its aqueous solubility limit quicker, but 

cannot be used to artificially enhance the water solubility of the chemical beyond its aqueous 

solubility limit. Control growth at 72 h should be greater than 16X and at 96 h greater than 

100X. The Coefficient of Variation (CV) between control replicates at 72 h and 96 h should be 

less than 20 percent. 

If there is no significant risk after the results of the acute toxicity testing have been integrated 

into the risk assessment, then no further testing is recommended. However, if there is a 

significant risk, then go to Tier 2.

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 
92 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk after the results of the aerobic biodegradation testing have been 

integrated into the risk assessment, then no further testing is recommended. However, if there 

is a significant risk, then go to Tier 3.

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (ai) and mean measured 

concentrations; dilution water hardness less than 150 mg/L as CaCO3; dilution water total 

organic carbon (TOC) less than 2.0 mg TOC/L; statistical analysis of effective concentrations at 

days 7, 14, 21, and 28; the highest treatment concentration on a nominal-basis should not exceed 

the aqueous solubility limit for the chemical; solvent can be used to assist the chemical to reach 

its aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility 

of the chemical beyond its aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be 

substituted for the 28-d ELS toxicity test because Van Leeuwen et al (1990) have demonstrated 

that the 7-d ELS toxicity test underestimated the chronic toxicity of anilines measured by the 

28-d ELS toxicity test by >5.3 times when the NOECs were compared (see Table VII in Van 

Leeuwen). Both anilines and allylic/vinyl/propargyl nitriles are more toxic than predicted 

based on narcosis alone, i.e., both classes have excess toxicity due to a more specific mode(s) of 

toxic action. A seven day exposure may not allow enough time for this excess toxicity to be 

expressed either because of not enough exposure and/or not enough time for metabolic 

activation. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(ai) and mean measured concentrations; dilution water hardness less than 150 mg/L as CaCO3; 

dilution water total organic carbon (TOC) less than 2.0 mg TOC/L; statistical analysis of 

effective concentrations at days 7, 14, and 21; the highest treatment concentration on a 

nominal-basis should not exceed the aqueous solubility limit of the chemical; solvent can be 

used to assist the chemical to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the chemical above its aqueous solubility limit; and 

the 7-d daphnid chronic toxicity test cannot be substituted for the 21-d toxicity test (Van 

Leeuwen et al 1990). 

If there is no significant risk after the results of the chronic toxicity testing have been integrated 

into the risk assessment, then no further testing is recommended. However, if there is a 

significant risk, then go to Tier 3.
93 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity 

tests (i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

acute toxicity test [Harmonized Test Guideline 850.6200], the avian acute oral toxicity test 

[Harmonized Test Guideline 850.2100), and the soil microbial community bioassay [Harmonized 

Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic toxicity 

testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), the avian 

reproductive toxicity test (Harmonized Test Guideline 850.2300), and the soil microbial 

community bioassay (Harmonized Test Guideline 850.5100). In addition, a fate test for 

biodegradability in soil (Harmonized Test Guideline 835.4100) may be recommended.

References: 

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334.

December 2007; revised June 2010 
94 

Category: Nonionic Surfactants Environmental Toxicity 

Definition. Any neutral structure having surfactant activity is considered a member of this 

category. Many of these surfactants have the following types of structure: 

Ethoxylate groups may be mixed with or be replaced by alcohol groups. Other neutral groups 

e.g. propoxylates, esters, halogens, may also be present. 

Hazard Concerns. Acute aquatic toxicity increases exponentially with increases in the 

hydrophobic chain length when the number of ethoxy groups or the hydrophilic component is 

held constant. In addition, when the number of carbons in the hydrophobe is constant, toxicity 

decreases with an increasing number of ethoxylate groups. The aquatic toxicity of members of 

the category can be predicted by structure-activity relationship (SAR). 

Boundaries. There are no established molecular weight boundaries for this category. Limits 

on chain length are inherent in the SARs. 

Testing. To address ecotoxicity concerns, base set acute aquatic toxicity testing (algae: static 

method, daphnid and fish: flow-through method, all measured concentrations). 

Tier 1. The acute aquatic base set of environmental toxicity tests will be recommended 

for aquatic exposures and the terrestrial base set of environmental toxicity tests (i.e., the early 

seeding growth test, the earthworm acute toxicity test and the soil microbial community 

bioassay) will be recommended for any terrestrial exposures. 

Acute fish toxicity test Harmonized Test Guideline 850.1075 

Acute daphnid toxicity test Harmonized Test Guideline 850.1010 

Green algae toxicity test Harmonized Test Guideline 850.5400 

Early seedling growth test Harmonized Test Guideline 850.4230 

Earthworm acute toxicity test Harmonized Test Guideline 850.6200 

Soil microbial community bioassay Harmonized Test Guideline 850.5100 

Tier 2. If acute toxicity testing indicates a significant risk, then environmental fate 
95 

testing in the form of aerobic biodegradation testing is recommended. Aerobic biodegradation 

testing may be conducted using either of the following test guidelines:

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

Tier 3. In addition, if acute toxicity testing indicates a significant risk, then chronic aquatic 

toxicity testing with fish and aquatic invertebrates will be recommended. 

Fish early life stage test Harmonized Test Guideline 850.1400 

Daphnid chronic toxicity testing Harmonized Test Guideline 850.1300 

September 1988, revised September 1996; revised June 2010 
96 

Category: Organotins Human Health 

Environmental Toxicity 

Definition. This category includes all mono-, di-, tri- and tetra-alkyl or phenyl organotin 

compounds, including organotin esters/oxides. The mode of toxic action of organotins in 

humans is unknown, but they are known to affect carbonate metabolism and other metabolic 

processes in the brain, liver, and muscle, as well as several enzymes and the oxidative activity of 

mitochondria. It has been suggested that general sulfhydryl binding may be responsible for the 

effects seen in mammals. It is assumed that these compounds need to be absorbed to be toxic, 

therefore, compounds with MWs > 1000 and which do not transform to organotin compounds 

with MWs < 1000 will be excluded from this category. Human health and aquatic toxicity for 

liquid organotins is assumed to be limited by the relative octanol/water partition coefficient (a 

relative Kow is based on the computer program, CLOGP, with C substituted for Sn). However, 

the limiting relative Kow value is unknown. The Agency has data for an organotin with a 

relative log Kow = 13.7 which still showed high toxicity towards fish and daphnids. Organotins 

which are solids at room temperature may show no toxicity at saturation at log Kow values < 13.7 

depending on the melting point, i.e., the higher the melting point at a given Kow, the greater the 

likelihood that no toxicity will be observed at saturation. For solids, the no-effects-at-saturation 

determination has to be made on a case-by-case basis. There are no known Kow limits for acute 

and chronic environmental toxicity at this time, but it is higher than a log Kow = 13.7. Future 

testing will determine the Kow limits. 

Hazard Concerns. Tested organotins have been shown to be from moderately irritating to 

corrosive to the skin and eyes. Acute oral and dermal exposures can result in systemic effects, 

primarily neurotoxicity. Concerns for immunotoxicity are based on data on dialkyltins and 

trialkyltins. During a 13-week oral study in rats using dioctyltin bis (2-ethylhexylthioglycolate), 

effects to the thymus, spleen, lymph nodes, and bone marrow were observed. A 

No-Observable-Adverse-Effect-Level (NOAEL) of 1.6 mg/kg/d was derived from this study. 

During a 17-month feeding study in rats using bis (tri-n-butyltin)-oxide, immunoglobulin E (IgE) 
97 

titers were reduced, as well as the activity of natural killer cells in the spleen, and there was 

reduced macrophage function. A NOAEL of 0.025 mg/kg/d was derived from this study. 

Based on the immunotoxicity end-point, an oral reference dose for chronic exposure (RfD) for 

tributyltin oxide of 3 x 10-5 mg/kg/d (IRIS 01/01/89) has been derived. Organotins are well 

known neurotoxins, with the tri- and tetra-substituted tins being more toxic than the mono- and 

di-substituted compounds. Although many tri-alkyltins show clear neurotoxic effects (e.g., 

lesions in the hippocampus), the neurotoxic potential of di-alkyltins has not been as well defined. 

Available data indicate that dibutyltin and dioctyltin can produce neurotoxic effects such as 

reductions in brain neurotransmitter levels, alterations in spontaneous motor activity and 

hindlimb weakness. An effect level for neurochemical and behavioral changes following 3 

days of oral administration of dibutyltin dilaurate was reported as 20 mg/kg. There are 

oncogenicity concerns for some of the organotins based on analogy to triphenyltin hydroxide, a 

group B probable human carcinogen. Therefore, the human health concerns for phenyltins will 

be dealt with on a case-by-case basis. 

The acute aquatic toxicity for several subclasses of organotins has been determined through 

toxicity testing (Vighi & Calamari, 1985; Wong et al. 1982) and structure activity relationships 

(SAR). Organotins have been shown to be highly toxic to green algae (Wong et al. 1982). 

The acute toxicity of organotins is moderate to high towards daphnids (Vighi & Calamari, 1985). 

One datum for fish has indicated high toxicity (USEPA 1996). Organotins exhibit toxicity 

ranging from moderate toxicity (i.e., > 10 mg/L) to high toxicity (i.e., < 1 mg/L) depending on 

their Kow , melting point, and MW. The higher the Kow, the higher the toxicity (or the lower the 

EC50 value). 

Boundaries. There are no known boundaries. The upper boundaries will be based on Kow

and MW. Acute toxicity expected with log Kow < 13.7; chronic toxicity has no known upper 

bound for log Kow, but it is > 13.7. MW will be < 1000 for stable compounds. The 

environmental base set of tests will be requested for aquatic releases and the terrestrial base set 

of tests will be recommended for terrestrial exposures. 

General Testing Strategy.

Tier 1. A 90-day subchronic test in rodents by the oral route with special attention to the 

lymphoid organs (thymus, spleen, peripheral lymph nodes) and bone marrow (Harmonized Test 

Guideline 870.3100). 

Neurotoxicity testing to include motor activity, a functional observational battery and 

neuropathology with special attention to lesions in the hippocampus (Harmonized Test Guideline 

870.6200). This testing can be combined with the 90-day subchronic protocol cited above. 

The acute aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures and the terrestrial base set of environmental toxicity tests will be recommended for 
98 

terrestrial exposures. The acute toxicity tests for fish and daphnids should be done using the 

flow-through method with measured concentrations. Effective concentrations should be based 

on 100% active ingredients (AI) and mean measured concentrations. Measure TOC of dilution 

water in the control just prior to testing. Ideally, the highest treatment concentration on a mean 

measured concentration-basis should equal the aqueous solubility limit. Solvent can be used to 

assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to significantly 

enhance the water solubility. The algal toxicity testing should be done with the static method 

and measured concentrations. Statistical analysis of effective concentrations at 24, 48, 72, and 

96 hours should be performed. The test medium should be used with at least 0.300 mg/L 

EDTA as a final concentration. 

Aquatic Base Set

Acute fish toxicity test Harmonized Test Guideline 850.1075 

Acute daphnid toxicity test Harmonized Test Guideline 850.1010 

Green algae toxicity test Harmonized Test Guideline 850.5400 

Terrestrial Base Set

Early seedling growth test Harmonized Test Guideline 850.4230 

Earthworm acute toxicity test Harmonized Test Guideline 850.6200 

Soil microbial community bioassay Harmonized Test Guideline 850.5100 

Tier 2. If acute aquatic toxicity testing indicates a significant risk, aerobic biodegradation 

testing is recommended. Aerobic biodegradability can be determined using either of the 

following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

Tier 3. If acute toxicity testing and environmental fate testing continue to indicate a significant 

risk, then chronic aquatic toxicity testing with fish and aquatic invertebrates is recommended 

with flow-through methods and measured concentrations. Effective concentrations should be 

based on 100% active ingredients (AI) and mean measured concentrations. Conduct statistical 

analysis of effective concentrations at days 7, 14, 21, and 28. Measure TOC of dilution water 

in the control just prior to testing. Ideally, the highest treatment concentration on a mean 

measured concentration-basis should be equal at the aqueous solubility limit. Solvent can be 

used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

significantly enhance the water solubility. The 7-d fish early life stage (ELS) toxicity test 

cannot be substituted for the 28-d ELS toxicity test and the 7-d daphnid chronic toxicity test 

cannot be substituted for the 21-d toxicity test because Van Leeuwen et al. (1990) have 

demonstrated that the 7-d ELS toxicity test underestimated the chronic toxicity of anilines 

measured by the 28-d ELS toxicity test by >5.3 times when the NOECs were compared (see 
99 

Table VII in Van Leeuwen). 

Chronic Aquatic Toxicity

Fish early life stage test Harmonized Test Guideline 850.1400 

Daphnid chronic toxicity testing Harmonized Test Guideline 850.1300 

References.

8E-594. 

Tributyltin oxide. Bis-(tri-n-butyltin)-oxide. (1988, December). Gesellschaft Deutscher 

Chemiker - Advisory Committee on Existing Chemical of Environmental Relevance 

(BUA). BUA Report 36. 

USEPA 1996. United States Environmental Protection Agency (1996). The Office of Pollution 

Prevention andToxics (OPPT) premanufacture notification (PMN) ECOTOX database: 

a confidential business information (CBI) collection of environmental toxicity data from 

new chemical submissions under Sec. 5 of the Toxic Substances Control Act (TSCA). 

Washington, DC: Environmental Effects Branch, Health and Environmental Review 

Division (7403), OPPT, USEPA. OPPT contact is V. Nabholz, 202-260-1271. 

Van Leeuwen, C.J., Adema, D.M.M., & Hermens, J. (1990). Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology, 16, 321-334. 

Vighi, M., & Calamari, D. (1985). QSARs for organotin compounds on Daphnia magna. 

Chemosphere, 14, 1925-1932. 

WHO 1980. World Health Organization Environmental Health Criteria 15. Tin and organotin 

compounds: A preliminary review. Geneva: WHO, pp. 59-62. 

Wong, P.T.S., Chau, Y.K., Kramar, O., & Bengert, G.A. (1982). Structure-toxicity relationship 

of tin compounds on algae. Canadian Journal of Fisheries and Aquatic Sciences, 39,

483-488. 

April 1991, revised September 1996. 
100 

Category: Peroxides Human Health (case-by-case) 

Environmental Toxicity 

Definition. Any molecular structure containing one or more of the following functional groups 

is considered to be a member of the class: 

 | | 

 -C-O-O-C- dialkyl peroxide

 | | 

 | 

 -C-O-O-H alkyl hydroperoxide

 | 

 O 

 ║ | 

 -C-O-O-C- peroxy ester

 | 

 O O 

 ║ ║

 -C-O-O-C- diacyl peroxide

 O 

 ║

 -C-O-O-H peroxy acid

The "typical" peroxide in the new chemical program is a discrete (class I) chemical with a 

molecular weight of <500. 

Hazard Concerns. EPA had previously identified hazard concerns for the possible 

carcinogenicity of new chemicals falling into the peroxide category based on available evidence. 

EPA has reviewed test data developed by the Society of the Plastics Industry (SPI) and others on 

the peroxide category of chemicals and concludes that available information does not support 

continued identification of peroxides as a new chemical category presenting concerns for 

possible carcinogenicity. EPA will continue to evaluate the potential health concerns for new 

chemical peroxides that are notified but, with this change, will not apply a category 

understanding as regards potential carcinogenicity. While the assessment of potential human 

health hazard concerns will be conducted on a case-by-case basis, this modification does not 

affect EPA=s approach to environmental hazard concerns which will continue to be identified for 

members of this category. 

Boundaries. There are no established boundary conditions for review of peroxides. 

General Testing Strategy. 
101 

The New Chemicals Program considers the following tests to be appropriate to address 

ecotoxicity concerns for peroxides: 

Base-set ecotoxicity testing to include fish (Harmonized Test Guideline 850.1075), 

daphnids (Harmonized Test Guideline 850.1010), and algae (Harmonized Test Guideline 

850.5400). 

Environmental fate testing including, as appropriate, melting point (Harmonized Test 

Guideline 830.7200) or boiling point (Harmonized Test Guideline 830.7220), water 

solubility (Harmonized Test Guideline 830.7840 or 830.7860), log Kow (Harmonized Test 

Guideline 830.7550, 830.7560, or 830.7570; or OECD 123, Partition Coefficient 

(1-Octanol/Water): Slow-Stirring Method), vapor pressure (Harmonized Test Guideline 

830.7950), hydrolysis (Harmonized Test Guideline 835.2120), photolysis (direct 

Photolysis (OECD 316) or Indirect Photolysis Screening Test (Harmonized Test 

Guideline 835.5270)), and aerobic biodegradation. 

Aerobic biodegradability can be determined using either of these two guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test 

Guideline 835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized 

Test Guideline 835.3140) 

September, 1988; revised June, 1994; revised April, 2001; revised June 2010 
102 

Category: Persistent, Bioaccumulative, 

and Toxic (PBT) Chemicals Health/Environmental Toxicity 

Environmental Fate 

Definition. PBT chemical substances possess characteristics of persistence (P) in the 

environment, accumulation in biological organisms (bioaccumulation (B)), and toxicity (T) that 

make them priority pollutants and potential risks to humans and ecosystems. Prominent 

examples of PBT chemical substances include the insecticide, DDT and polychlorinated 

biphenyls (PCBs). This PBT category includes the boundary conditions, such as fish 

bioconcentration/bioaccumulation factors and environmental persistence values, that would 

determine inclusion in (or exclusion from) the category, and standard hazard and fate tests to 

address P, B, and T concerns for the chemical substances fitting the category description. For 

background information and discussion of this PBT category, see 

http://www.epa.gov/oppt/newchems/pbtpolcy.htm, and the proposed (October 5, 1998; 63 FR 

53417) and final (November 4, 1999; 64 FR 60194) ACategory for Persistent, Bioaccumulative, 

and Toxic Chemical Substances@ published in the US Federal Register. 

Hazard Concerns. Generally, PBT chemical substances are chemical substances that partition 

to water, sediment or soil and are not removed at rates adequate to prevent their bioaccumulation 

in aquatic or terrestrial species, with the potential to pose a risk via food chain toxicity. 

Boundaries. The following table summarizes specific identification criteria and associated 

process for use in evaluating new chemical PBT substances. 

NEW CHEMICALS PROGRAM 

PBT CATEGORY CRITERIA AND PROCESS

 TSCA Section 5 Action 

5(e) Order/Significant New 

Use Rule (SNUR)

Exposure/release controls 

included in order; testing 

required

 Ban Pending Testing

Deny commercialization; testing results 

may justify removing chemical from Ahigh 

risk concern@

 Persistence 

(transformation half-life)

>2 months >6 months 

 Bioaccumulation* 

(Fish BCF or BAF)

>1000 >5000 

 Toxicity Develop toxicity data where necessary, based upon various 

factors, including concerns for P, B, other physical/chemical 

factors, and toxicity. 

*Chemicals must also meet criteria for MW (<1000) and cross-sectional diameter (<20D, or <20 x 10 -8 cm). BCF 
103 

of 1000 and 5000 are equivalent to log Kow of 4.2 and 5, respectively.

General Testing Strategy

Tier 1. Based upon SAR and professional judgment, the Agency identifies a new chemical 

substance as a possible PBT chemical substance.

Log Kow Liquid chromatography (Harmonized Test Guideline 

830.7570/OECD 117) or generator column (Harmonized 

Test Guideline 830.7560) method; or OECD 123, Partition 

Coefficient (1-Octanol/Water): Slow-Stirring Method 

Ready biodegradability Ready biodegradability (Harmonized Test Guideline 

835.3110/OECD 301) 6 methods (choose one): DOC 

Die-Away, CO2 Evolution, Modified MITI (I), Closed 

Bottle, Modified OECD Screening, Manometric 

Respirometry 

or 

Sealed-vessel CO2 production test (Harmonized Test 

Guideline 835.3140) 

Hydrolysis in water (if, 

based upon SAR, 

susceptibility to hydrolysis is 

suspected) 

Harmonized Test Guideline 835.2120 (OECD 111) 

Results If the measured log Kow is <4.2 or if the test chemical 

passes the ready biodegradability test (i.e., not persistent in 

the environment), no further PBT-related testing is required. 

If the measured log Kow is greater than or equal to 4.2 and 

the chemical does not pass the ready biodegradability test, 

the chemical would require tier 2 testing. If hydrolysis 

testing is conducted and results in a half-life of <60 days, 

further testing may not be needed, but the need for testing 

must be determined after consideration of factors specific to 

the case, such as physical/chemical properties, persistence 

and bioaccumulative qualities of hydrolysis products, and 

the nature of the expected releases. 
104 

Tier 2. Biodegradability and Bioaccumulation

Biodegradability Shake-flask die-away test (Harmonized Test Guideline 

835.3170) or Aerobic Mineralization in Surface Water – 

Simulation Biodegradation Test (Harmonized Test Guideline 

835.3190/OECD 309) 

Bioaccumulation Fish bioconcentration test (Harmonized Test Guideline 

850.1730/OECD 305), or an equivalent test). Measured 

BCF should be based on 100 percent active ingredient and 

measured concentration(s). 

Results If the measured biodegradation half-life is >60 days and

measured BCF is >1000, tier 3 testing will be required. If 

only one condition is met, releases and exposure are further 

considered to determine if additional testing is required. 

Tier 3. Toxicity/advanced environmental fate testing.

Human health toxicity Combined repeated dose oral toxicity with the 

reproductive/developmental toxicity screening test (OECD 

No. 422) in rats. Other health testing will be considered 

where appropriate. 

Environmental fate Sediment/water microcosm biodegradation test (Harmonized 

test Guideline 835.3180) or Aerobic/anaerobic aquatic 

metabolism (Harmonized test Guideline 835.4300/835.4400 

Chronic environmental 

toxicity 

Fish (rainbow trout) and daphnids should be tested 

according to Harmonized Test Guideline 850.1400 (same as 

OECD 210) and Harmonized Test Guideline 850.1300 (same 

as OECD 202), respectively. Additional testing to evaluate 

other biota (e.g., avian, sediment dwelling organisms) or 

other effects (e.g., endocrine disrupting potential) will be 

considered where appropriate. 

November, 1999 
105 

Category: Phenolphthaleins Human Health 

Definition. Any chemical containing the phenolphthalein structure is considered to be a 

member of the category. 

Hazard Concerns. The health concern for phenolphthalein and derivatives of phenolphthalein 

is for cancer based on the NTP cancer study (NTP report TR-465, November 1996) for 

phenolphthalein with administration via the diet. There was clear evidence of carcinogenic 

activity in male F344/N rats based on markedly increased incidences of benign 

pheochromocytomas of the adrenal medulla and of renal tubule adenomas and adenomas or 

carcinomas (combined). There was some evidence of carcinogenic activity in female F344/N 

rats based on the increased incidences of benign pheochromocytomas of the adrenal medulla in 

the 12,000 ppm group and of benign or malignant pheochromocytomas (combined) in the 12,000 

and 25,000 ppm groups. There was clear evidence of carcinogenic activity in male B6C3F1

mice based on increased incidences of histiocytic sarcomas and of malignant lymphomas of 

thymic origin. There was clear evidence of carcinogenic activity in female B6C3F1 mice based 

on increased incidences of histiocytic sarcomas, malignant lymphomas of all types, lymphomas 

of thymic origin, and benign sex-cord stromal tumors of the ovary. 

Boundaries. No boundaries currently defined.

Testing. EPA considers the following tests to be the most appropriate for phenolphthalein 
106 

derivatives found to pose an unreasonable risk to human health: 

Tier 1. 

Comparative dermal and oral absorption study in rats (Harmonized Test Guideline, 

870.7485) 

In vitro Chromosome aberrations study in Chinese hamster ovary cells with 

phenolphthalein as an additional positive control (Harmonized Test Guideline 870.5375) 

Log Kow test (Harmonized Test Guideline 830.7550, 830.7560, or 830.7570; or OECD 

123, Partition Coefficient (1-Octanol/Water): Slow-Stirring Method) 

Water solublility for both lactone and acid form (Harmonized Test Guideline 830.7840 or 

830.7860) 

Ready biodegradability (Harmonized Test Guideline 835.3110) 

Tier 2. 

2-year carcinogenicity study in mice (Harmonized Test Guideline 870.4200) 

April, 1998 
107 

Category: Phenols Environmental Toxicity 

Definition. This category includes phenols (i.e., monophenols), polyhydroxy phenols, and 

polyphenols. It is assumed that these compounds need to be absorbed to be toxic; therefore, 

compounds with MWs > 1000 will be excluded from this category. Acute toxicity for phenols 

which are liquids at room temperature is known to be limited by the octanol/water partition 

coefficient (Kow). Above a log Kow value of about 7.38, phenols are expected to show no 

effects at saturation during 96-h exposures (Veith and Broderius 1987). Phenols which are 

solids at room temperature may show no toxicity at saturation at lower Kow values depending on 

the melting point, i.e., the higher the melting point at a given Kow, the greater the likelihood that 

no toxicity will be observed at saturation. For solids, no effects at saturation has to be 

demonstrated on a case-by-case basis. There are no known Kow limits for chronic toxicity at 

this time, but it may not be much above a log Kow = 9.0 for liquid phenols. Future testing will 

determine this Kow limit. 

Hazard Concerns. The aquatic toxicity for phenols has been determined through SAR 

analysis by EPA using ECOSAR – a hazard estimation tool that uses chemical structure 

descriptors to estimate the acute and chronic toxicity of a substance to aquatic organisms. [Link 

for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. Members of this 

category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high toxicity (i.e., < 1 

mg/L) depending on their Kow, MW, and substitutions (e.g., dinitrophenols). 

Dinitrophenols are known to be more toxic than predicted by these SARs (see the category for 

polynitroaromatics). 

Environmental Fate. Phenols are subject to indirect photolysis under environmentally 

realistic conditions. 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW. Acute toxicity expected with log Kow < 7.38; no effects at saturation during 96-h 

exposures when log Kow >= 7.38. Chronic toxicity has no known upper bound for log Kow, but 

it is probably near 9. MW will be < 1000. The environmental base set of tests will be 

requested for aquatic releases and the terrestrial base set of tests will be recommended for 

terrestrial exposures. When the log Kow is >= 7.38, chronic toxicity testing with fish, daphnids, 

and green algae will be recommended. 

General Testing Strategy 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 
108 

measured concentrations; effective concentrations will be based on 100% active ingredients (AI) 

and mean measured concentrations; measured TOC of dilution water in the control; the highest 

treatment concentration on a nominal-basis should equal the aqueous solubility limit; and solvent 

can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% AI and mean 

measured concentrations; statistical analysis of effective concentrations at 24, 48, 72, and 96 

hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the highest 

treatment concentration on a nominal-basis equal to the aqueous solubility limit; and solvent can 

be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

If there is no significant risk from the PMN after the results of the environmental base set have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water— Indirect Photolysis Screening Test 

(Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, go to Tier 

4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then prepare 

a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. For example, the most 

sensitive species from the environmental base set has an EC50 value = 2.0 mg PMN/L (based on 

100% AI, therefore, prepare a 5.0 mg PMN per liter stock solution based on 100% AI using the 

standard humic-containing solution. This stock solution is exposed to sunlight for at least 6 

half-lives to ensure that all of the PMN has been photolyzed, and then this stock solution is used 

to retest the most sensitive aquatic species to determine if the photolysis products of the PMN 

are more or less toxic that the PMN. 

Tier 4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% AI and mean measured concentrations; statistical 

analysis of effective concentrations at days 7, 14, 21, and 28; measured TOC of dilution water in 

the control; the highest treatment concentration on a nominal-basis should be set at the aqueous 

solubility limit; solvent can be used to assist the PMN to reach its aqueous solubility limit 

quicker, but cannot be used to artificially enhance the water solubility of the PMN beyond its 
109 

aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be substituted for the 28-d 

ELS toxicity test because Van Leeuwen et al (1990) have demonstrated that the 7-d ELS toxicity 

test underestimated the chronic toxicity of anilines measured by the 28-d ELS toxicity test by 

>5.3 times when the NOECs were compared (see Table VII in Van Leeuwen); 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% AI and mean 

measured concentrations; statistical analysis of effective concentrations at days 7, 14, and 21; 

measured TOC of dilution water in the control; the highest treatment concentration on a 

nominal-basis should be set at the aqueous solubility limit; solvent can be used to assist the PMN 

to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the water 

solubility of the PMN beyond its aqueous solubility limit; and the 7-d daphnid chronic toxicity 

test cannot be substituted for the 21-d toxicity test because Van Leeuwen et al (1990) have 

demonstrated that the fish 7-d ELS toxicity test underestimated the chronic toxicity of anilines 

measured by the fish 28-d ELS toxicity test by >5.3 times when the NOECs were compared (see 

Table VII in Van Leeuwen). 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200] and the soil microbial community bioassay 

[Harmonized Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic 

toxicity testing for terrestrial organisms include: the plant whole life cycle test (Harmonized Test 

Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 850.4800), and the soil 

microbial community bioassay (Harmonized Test Guideline 850.5100). 

References.

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

Veith GD and Broderius SJ. 1987. Structure-toxicity relationships for industrial chemicals 

causing type (II) narcosis syndrome. In Kaiser KLE (ed), QSAR In Environmental Toxicology 

-II, pp. 385-391. Reidel Publishing Company. 

July, 1991; revised June 2010 
110 

Category: Phosphates, Inorganic

Definition. This category includes all inorganic soluble forms of phosphates, such as, 

phosphoric acid [PO4H3 or OP(=O)(O)O] and its salts or phosphate salts, pyrophosphates, 

polyphosphates, and organic and inorganic forms of phosphorous that can be oxidized to 

phosphates rapidly. Inorganic forms of phosphonic acid (H2PO3 or OP(=O)O) are not included 

in this category because monopotassium phosphonic acid [13977-65-6] has been shown not to be 

an algal nutrient, not to be a replacement for phosphate in algal growth medium, and not to cause 

exponential growth of green algae. 

Hazard Concerns. The standard environmental toxicity profile for inorganic phosphates as P 

in mg P/L is: 

ECOTOX: Predicted (P) and measured (M) toxicity values in mg/L (ppm) are: 

fish 96-h LC50 > 100.0 P 

daphnid 48-h LC50 > 100.0 P 

green algal 96-h EC50 b < 0.030 P 

algal 96-h EC290 b = 0.030 M, S,N 

fish chronic value > 10.0 P 

daphnid ChV > 10.0 P 

algal ChV = 0.010 M, Hutchinson 1957 

Predictions are based on SAR-nearest analog analysis for soluble forms of inorganic phosphates 

(PO4); SAR chemical class = P-O4; MW of P = 31, PO4 = 95, PO4H3 = 98; pH7; effective 

concentrations based on 100% active ingredients and nominal concentrations of P; hardness 

<24.0 mg/L as CaCO3; and TOC <2.0 mg/L; high concern for eutrophication; 

assessment factor = 10.0 

concern concentration = 0.001 

Phosphate phosphorus has the potential to stimulate the growth of green algae and cause algal 

blooms and eutrophication in freshwater and marine environments. The phosphate anion is a 

plant nutrient and is the major limiting nutrient in many freshwater environments. The USEPA 

OW WQC (USEPA 1976) states: 

When such concentrations [of total phosphate phosphorus] exceed 25 μg/l at the time of the 

spring turnover on a volume-weighted basis in lakes or reservoirs, they may occasionally 

stimulate excessive or nuisance growths of algae and other aquatic plants. Algal growths 

impart undesirable tastes and odors to water, interfere with water treatment, become aesthetically 

unpleasant and alter the chemistry of the water supply. They contribute to the phenomenon of 

cultural eutrophication. 

To prevent the development of biological nuisances and to control accelerated or cultural 

eutrophication, total phosphates as phosphorus (P) should not exceed 50 μg/l in any stream at the 
111 

point where it enters any lake or reservoir, nor 25 μg/l within the lake or reservoir. A desired 

goal for the prevention of plant nuisances in streams or other flowing waters not discharging 

directly to lakes or impoundments is 100 μg/l total P (Mackenthum, 1973). Most relatively 

uncontaminated lake districts are known to have surface waters that contain from 10 micrograms 

P/L (or 31 micrograms PO4H3/L) to 30 microg P/L (or 92 microg PO4H3/L) (Hutchinson, 

1957). 

Odum (1971) called phosphorus a major factor in the process of cultural eutrophication. 

Eutrophication results when nutrients, especially phosphates, are imported into aquatic 

ecosystems. This process is analogous to fertilizing an agricultural field. Phosphates act like 

a fertilizer and produce increases in the abundance of algae and other aquatic plants; eventually, 

they can result in excessive growths of algae (i.e., algal blooms). Excessive algae can block 

sunlight from reaching submerged macrophytes and other microalgae below the surface. When 

the algae die and fall to the bottom of slow-moving water or lakes, they are consumed by 

bacteria which use up available oxygen producing anaerobic conditions. Decaying algae cause 

odors and oxygen depletion of the water to occur with concomitant detriment to fish and aquatic 

invertebrates and, in turn, fishing and water-based recreational activities. 

Phosphate concentrations as low as 0.050 mg P/L (ppm) or 50.0 micrograms P/L (ppb) will 

produce exponential growth of green algae in 96 hours (Miller et al. 1978), and phosphate 

concentrations from 10 to 60 micrograms P/L (ppb) were correlated to algal blooms and oxygen 

depletion (i.e., eutrophication) in Lake Washington, Seattle (Odum 1971). Phosphates have 

been severely limited or banned from detergents in 13 states, the District of Columbia, and 

several counties and municipalities (USEPA 1992). Sodium tripolyphosphate was one of the 

principal components of synthetic detergents. Freshwater green algae are clearly the most 

sensitive group of aquatic organisms to phosphate additions to water. 

Boundaries. The boundaries for inorganic phosphate compounds depend on the release of 

inorganic phosphates which can be used by algae as a mineral nutrient. Any inorganic 

phosphate which can be used by algae as a nutrient or which transforms to release or becomes an 

algal nutrient is included in this category. 

Testing. Based on a consideration of available data on inorganic phosphates and the 

physicochemical properties of these compounds, there is no need for further testing. However, 

if there is doubt about the availability of phosphate in a nutrient form from a PMN substance, 

then the algal toxicity test can be done with the PMN substance substituted for phosphate 

nutrient in the algal growth medium. If a PMN substance is capable of stimulating exponential 

growth green algae, it must be emphasized that inorganic phosphates should not be released to 

water because of their potential to cause eutrophication and their persistence. 

Regulatory Actions.

(1) Phosphates have been severely limited or banned from detergents in 13 states, the District 

of Columbia, and several counties and municipalities (USEPA 1992). 

(2) Water Quality Criterion, 1976 (USEPA 1976): total phosphates as phosphorus (P) should 
112 

not exceed 50 micrograms p/L in any stream at the point where it enters any lake or reservoir, 

nor 25 micrograms P/L within the lake or reservoir. 

(3) Hazard assessments of selected aqueous cleaner chemicals, USEPA (1990): OPPT 

recommendation to the Office of Air and Radiation: "...phosphates should never be released to 

water." 

(4) Agency recommendation for a "nationwide elimination of the use of household laundry 

detergents containing phosphates." (USEPA 1992). 

References.

Hutchinson, G. E., 1957, A treatise on limnology. New York, NY: John Wiley & Sons. 

Mackenthun, K. M., 1973, Toward a cleaner aquatic environment. Washington, DC: USEPA. 

Miller, W. E., Greene, J. C., and Shiroyama T. 1978. The Selenastrum capricornutum Printz 

algal assay bottle test. Corvallis, OR: USEPA, Office of Research and Developmental, 

Environmental Research Laboratory-Corvallis, EPA-600-9-78-018. 

United States Environmental Protection Agency (USEPA). 1976. Quality Criteria for Water. 

 EPA-440/9-76-023. Washington, DC: Office of Water Planning and Standards, OW, 

USEPA. Available from NTIS, Springfield, VA 22161, PB-263-943. 

United States Environmental Protection Agency (USEPA). 1990. (Health and environmental 

effects of selected aqueous cleaner chemicals. Washington, DC: Health and Environmental 

Review Division, Office of Pollution Prevention and Toxics, USEPA. 

United States Environmental Protection Agency (USEPA). 1992. (DRAFT Phosphate 

detergents: An evaluation of the benefits and costs of eliminating their use in the United States. 

Washington, DC: Environmental Results Branch, Office of Policy, Planning, & Evaluation, 

USEPA. 

March 2000 
113 

Category: Phosphinate Esters Environmental Toxicty 

Definition. Phosphinate esters are a class of organic compounds characterized by the 

functional group R-O-P(=O)(R)R. Phosphinate esters are metabolically active and exhibit 

excess aquatic toxicity in addition to narcosis. Phosphinate esters exhibit excess toxicity 

relative to simple esters (-C(=O)O-) and phosphate esters (-OP(=O)(O-)O-. 

It is assumed that phosphinate esters need to be absorbed to be toxic, therefore, phosphinate 

esters with MW >1000 will be excluded from this category. Acute toxicity for phosphinate 

esters is known to be correlated and limited by the octanol/water partition coefficient (Kow). 

Above a log Kow value of >5.0, phosphinate esters show no effects at saturation during 96-hr 

exposures to fish. Phosphinate esters which are solids at room temperature may show no 

toxicity at saturation at lower Kow values depending on the melting point, i.e., the higher the 

melting point at a given Kow, the greater the likelihood that no toxicity will be observed at 

saturation. For solids, the no effects at saturation has to be determined on a case-by-case basis. 

 There are no measured upper Kow limits for chronic toxicity at this time, but it may not be much 

above a log Kow = 8. 

Hazard Concerns. The aquatic toxicity for phosphonate esters has been determined through 

SAR analysis by EPA using ECOSAR – a hazard estimation tool that uses chemical structure 

descriptors to estimate the acute and chronic toxicity of a substance to aquatic organisms. [Link 

for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

Environmental Fate. Phosphinate esters hydrolyze in water and their rate of hydrolysis is 

correlated with pH. The more alkaline, the faster the hydrolysis. The SAR for hydrolysis is: 

Log hydrolysis t1/2 (d) = 4.325 -0.497 pH 

where n=2, R2

=1.0. 

At pH 7.1, the hydrolysis t1/2 = 6.3 days or 150 hours. 

Boundaries. MW <1000. Log Kow <5.0 for acute toxicity to fish and aquatic invertebrates; 

log Kow <6.4 for toxicity to green algae as a 96-h EC50; and log Kow assumed to be <8.0 for 

chronic toxicity to aquatic organisms, but could be higher. 

General Testing Strategy. 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (ai) 

and mean measured concentrations; measured TOC of dilution water in the control; ideally, 
114 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; and solvent can be used to assist the aldehyde to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the test 

chemical significantly above its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(ai) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; ideally, 

mean measured concentrations in the highest treatment concentration should be equal the 

aqueous solubility limit; and solvent can be used to assist the aldehyde to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the test 

chemical significantly above its aqueous solubility limit. 

If there is no significant risk from the PMN chemical after the results of the environmental base 

set have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the PMN chemical after the results of biodegradation testing 

have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; 

measured TOC of dilution water in the control; ideally, mean measured concentrations in the 

highest treatment concentration should be equal to the aqueous solubility limit; solvent can be 

used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN significantly above its aqueous solubility 

limit; and the 7-d ELS stage toxicity test cannot be substituted for the 28-d ELS toxicity test 

because the 7-d ELS toxicity test may underestimate chronic toxicity measured by the 28-d ELS 

toxicity test when the Chronic Values are compared. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; ideally, mean measured 
115 

concentrations in the highest treatment concentration should be equal to the aqueous solubility 

limit; solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but 

cannot be used to artificially enhance the water solubility of the PMN significantly above its 

aqueous solubility limit; and the 7-d daphnid chronic toxicity test cannot be substituted for the 

21-d toxicity test because the daphnid 7-d short-term chronic toxicity test may underestimate 

chronic toxicity measured by the daphnid 21-d chronic toxicity test when the chronic values are 

compared. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200], and the soil microbial community bioassay 

[Harmonized Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic 

toxicity testing for terrestrial organisms include: the plant whole life cycle test Harmonized Test 

Guideline 850.4150), the plant uptake test Harmonized Test Guideline 850.4800), and the soil 

microbial community bioassay (Harmonized Test Guideline 850.5100). 

September 1996; revised June 2010. 
116 

Category: Polyanionic Polymers (& Monomers Environmental Toxicity 

Definition. There are two subcategories of polymers that are of concern: 

- Polyaromatic sulfonates - condensation products of sulfonated aromatics with 

formaldehyde, and 

 

 - Polyacrylates with free carboxyl groups 

This category includes monomers with two or more acid groups and which act like organic acid 

chelators. The acid groups may include carboxylic acids, silicic acids, phosphoric acid, and 

sulfuric acids. These acids may also contain thiol substitutions. The acid groups on a 

monomer may be all of the same type of acid or may be a mixture of acids. The monomeric 

nucleus may include carbon, silica, oxygen, sulfur, and nitrogen, or mixtures of these elements. 

Members of this category must be water soluble or water self-dispersing. Molecular weights 

can be > 1000. 

Hazard Concerns. Polyaromatic sulfonates are moderately toxic to fish, daphnids, and algae. 

The polyacrylates are toxic to algae only. Polyanionic monomers (as salts, e.g., Na or K salts) 

are moderately toxic to green algae, but show low toxicity to fish and daphnids. It is assumed 

that the toxicity of these compounds is due to over-chelation of nutrient elements needed for 

algal growth and that this toxicity will be mitigated in the presence of Ca++ either added to the 

compound before testing or present in the growth/test medium at a hardness of about 150 mg/L 

as CaCO3. 

Boundaries. Polymers must be water-soluble. Molecular weights are generally >1,000. 

General Testing Strategy 

To address ecotoxicity concerns, for polycarboxylic acids (polyacrylates) and polyanionic 

monomers, algal testing (static methods, nominal concentrations) is recommended, in 3 separate 

tests: 1) the test substance as is, 2) with equivalent of calcium ion, and 3) with growth medium at 

150 mg/L hardness, as CaCO3). For polyaromatic sulfonates, base set aquatic toxicity testing 

(flow through methods, measured concentrations) in algae, daphnids, and fish is recommended. 

September, 1988; revised April, 1991 
117 

Category: Polycationic Polymers Environmental Toxicity 

Definition. Any polymer that exists in the environment with multiple positive charges is a 

member of this class. Such structures include polyamines, polyquaternary ammonium, 

polysulfonium, and polyphosphonium compounds. 

Hazard Concerns. Members of the category are toxic to fish, invertebrates, and algae. Algae 

are six-fold more sensitive than fish and daphnids. It is presumed that these compounds act on 

the surface of organisms and need not be absorbed. Toxicity increases exponentially with 

increasing charge density at cationic equivalent weights of >400. At lower charge equivalent 

weights, toxicity does not increase. A number of QSARs (quantitative structure-activity 

relationships) have been developed to predict the toxicity of polycationic polymers. 

Boundaries. Polymers must be water-soluble or water-dispersible. Molecular weights are 

>300 although the typical new chemical polycationic polymer has a molecular weight in excess 

of 1000. EPA has been engaged in discussions with the Cationic Flocculant Producers 

Association in an attempt to identify and develop a set of tests on representative polycationic 

polymers which could better define the limits of the category. 

General Testing Strategy 

To address ecotoxicity concerns, for polymers with % amine nitrogen <0.7% and >0.1%: base 

set acute aquatic toxicity testing in algae, daphnids, and fish, plus humic acid testing in fish (20 

mg/L humic acid in dilution water and 10 mg/L) is recommended. All testing uses static 

method, nominal concentrations. For some members of the class, a test of sorbed chemical 

using a benthic organism may also be recommended. 

September, 1988; periodically revised. 
118 

Category: Polynitroaromatics Environmental Toxicity 

Definition. This category includes all dinitroaromatics and trinitroaromatic compounds, for 

example, dinitrobenzenes, dinitroanilines, dinitrophenols, and dinitropyridines. 

Polynitroaromatics probably act by uncoupling of oxidative phosphorylation (Doull et al 1980). 

It is assumed that these compounds need to be absorbed to be toxic; therefore, compounds with 

MWs > 1000 will be excluded from this category. Acute toxicity for polynitroaromatics which 

are liquids at room temperature is assumed to be limited by the octanol/water partition 

coefficient (Kow). Above a log Kow value of ≥ 7.00 (based on test data for anilines reported 

Veith and Broderius 1987), polynitroaromatics are not expected to show toxic effects at 

saturation during 96-h exposures. Polynitroaromatics which are solids at room temperature 

may show no toxicity at saturation at lower Kow values depending on the melting point, i.e., the 

higher the melting point at a given Kow, the greater the likelihood that no toxicity will be 

observed at saturation. For solids, the no effects at saturation has to be determined on a 

case-by-case basis. There are no known Kow limits for chronic toxicity at this time, but it may 

not be much above a log Kow = 10 for liquid polynitroaromatics. 

Hazard Concerns. The aquatic toxicity for several classes of polynitroaromatics have been 

determined through SAR analysis by EPA using ECOSAR – a hazard estimation tool that uses 

chemical structure descriptors to estimate the acute and chronic toxicity of a substance to aquatic 

organisms. [Link for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

Members of this category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high 

toxicity (i.e., < 1 mg/L) depending on their Kow and MW. 

Environmental Fate. Polynitroaromatics are expected to be subject to rapid direct and indirect 

photolysis under environmentally realistic conditions. 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW. Acute toxicity expected with log Kow < 7.0; no effects at saturation during 96-h 

exposures when log Kow ≥ 7.0. Chronic toxicity has no known upper bound for log Kow, but it 

is probably near 10. MW will be < 1000. The environmental base set of tests will be 

requested for aquatic releases and the terrestrial base set of tests will be recommended for 

terrestrial exposures. When the log Kow is ≥ 7.0, chronic toxicity testing with fish and daphnids 

will be recommended. 

General Testing Strategy. 

I. Release to Aquatic Ecosystems: 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (AI) 

and mean measured concentrations; measured TOC of dilution water in the control; the highest 
119 

treatment concentration on a nominal-basis should equal the aqueous solubility limit; and solvent 

can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the 

highest treatment concentration on a nominal-basis equal to the aqueous solubility limit; and 

solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be 

used to artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

If there is no significant risk from the PMN after the results of the environmental base set have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water— Indirect Photolysis Screening Test 

(Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, go to Tier 

4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then prepare 

a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. For example, if the most 

sensitive species from the environmental base set has an EC50 value = 2.0 mg PMN/L (based on 

100% active ingredients [AI]), then prepare a 5.0 mg PMN per liter stock solution based on 

100% AI using the standard humic-containing solution. This stock solution is exposed to 

sunlight for at least 6 half-lives to ensure that all of the PMN has been photolyzed, and then this 

stock solution is used to retest the most sensitive aquatic species to determine if the photolysis 

products of the PMN are more or less toxic that the PMN. 

Tier 4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured 

TOC of dilution water in the control; the highest treatment concentration on a nominal-basis 

should be set at the aqueous solubility limit; solvent can be used to assist the PMN to reach its 

aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility of 

the PMN beyond its aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be 

substituted for the 28-d ELS toxicity test because Van Leeuwen et al (1990) have demonstrated 

that the 7-d ELS toxicity test underestimated the chronic toxicity of anilines measured by the 

28-d ELS toxicity test by >5.3 times when the NOECs were compared (see Table VII in Van 
120 

Leeuwen); 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; the highest treatment concentration 

on a nominal-basis should be set at the aqueous solubility limit; solvent can be used to assist the 

PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the 

water solubility of the PMN beyond its aqueous solubility limit; and the 7-d daphnid chronic 

toxicity test cannot be substituted for the 21-d toxicity test because Van Leeuwen et al (1990) 

have demonstrated that the fish 7-d ELS toxicity test underestimated the chronic toxicity of 

anilines measured by the fish 28-d ELS toxicity test by >5.3 times when the NOECs were 

compared (see Table VII in Van Leeuwen). 

Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

(i.e., the early seedling growth test [Harmonized Test Guideline 850.4230], the earthworm 

toxicity test [Harmonized Test Guideline 850.6200], and the soil microbial community bioassay 

[Harmonized Test Guideline 850.5100]) will be recommended for terrestrial exposures. Chronic 

toxicity testing for terrestrial organisms include: the plant whole life cycle test Harmonized Test 

Guideline 850.4150), the plant uptake test Harmonized Test Guideline 850.4800), and the soil 

microbial community bioassay (Harmonized Test Guideline 850.5100). 

References.

Doull J, Klaassen CD, and Amdur MO. 1980. Casarett and Doull's Toxicology. The Basic 

Science of Poisons. Second Ed. New York, NY: Macmillan Pub. Co., Inc. 

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

Veith GD and Broderius SJ. 1987. Structure-toxicity relationships for industrial chemicals 

causing type (II) narcosis syndrome. In Kaiser KLE (ed), QSAR In Environmental Toxicology 

-II, pp. 385-391. Boston, MA: D. Reidel Publishing Company. 

May, 1991; revised June 2010
121 

Category: Respirable, Poorly Soluble Particulates Health Only 

Definition. This category includes a variety of inorganic, poorly soluble (as designated in ILSI 

2000) particulates. Typically, they are oxides of various metals or nonmetals (i.e., silicon) 

Boundaries. There is a potential for respirability if there are any particles ≤10 μ in diameter in 

the material being handled by workers. Summarized below are currently available test data on 

five different poorly soluble particulates: silica, talc, titanium dioxide, PMN 96-175 (lithium 

manganese oxide), and carbon black. The suitability of one or more of these analogues for a 

particular PMN particulate must be determined on a case-by-case basis. Risk is to be assessed 

by the margin of exposure method for the reason stated in the next paragraph. 

Hazard Concerns. The category concerns discussed here are limited to effects on the lung as a 

result of inhaling the particles. Broadly, as shown in rat inhalation studies, these effects range 

from inflammation to fibrosis to, potentially, cancer. Because it is still not known with 

certainty whether high lung burdens of poorly soluble particulates can lead to lung cancer in 

humans via mechanisms similar to those of the rat, in the absence of mechanistic data to the 

contrary, it must be assumed that the rat model can identify potential carcinogenic hazards to 

humans. Since the apparent responsiveness of the rat model at overload is dependent on 

coexistent chronic active inflammation and cell proliferation, at lower lung doses in which 

chronic active inflammation and cell proliferation are not present, no lung cancer hazard is 

anticipated (ILSI 2000). 

Some of the particulates may contain metals, for example, chromium, that may present other and 

more imminent toxicities, depending on the bioavailability of the metal ions. Thus, the 

toxicities of the metal components of the particulates must also be assessed, and on a 

case-by-case basis.

Lung Toxicity of Five Poorly Soluble Particulates 

1. Fibrogenicity/Carcinogenicity of Crystalline Silica

Humans. Based on sufficient evidence for the carcinogenicity of inhaled crystalline silica from 

occupational sources, the International Agency for Research on Cancer (IARC, 1997) has 

classified crystalline silica as a Group 1 carcinogen in humans. According to IARC, studies of 

the following populations provided the least-confounded examinations of an association between 

silica exposure and cancer risk: gold miners, stone industry workers, granite shed and quarry 

workers, crushed stone industry workers, diatomaceous earth industry workers, refractory brick 

workers, pottery workers, and cohorts of registered silicotics. Not all of these studies 

demonstrated excess cancer risks; but, in view of the large number of epidemiological studies 

undertaken and the wide range of populations and exposure circumstances, some nonuniformity 

of results would be expected. In some studies, increasing risk gradients have been observed in 

relation to dose surrogates--cumulative exposure, duration of exposure, or the presence of 

radiographically defined silicosis--and, in one instance, to peak intensity exposure. For these 
122 

reasons, the IARC Working Group concluded that overall, the epidemiological findings support 

increased lung cancer risks from inhaled crystalline silica resulting from occupational exposure. 

Animals. IARC (1997) has concluded that there is Asufficient evidence in experimental animals 

for the carcinogenicity of crystalline silica. A number of studies (rev. in: IARC, 1997; Woo et 

al., 1988; Holland, 1990) have demonstrated that, in addition to silicosis/fibrosis, pulmonary 

tumors are induced in rats exposed to quartz (Mini-U-Sil; a common form of crystalline silica) 

by inhalation, single intrapleural, intraperitoneal, and/or intratracheal administration. In a 

24-month inhalation study in rats, the lowest tested dose of respirable crystalline silica particles 

to induce lung tumors (Lowest Observed Adverse Effect Level, or LOAEL) was 0.74 mg/m3. 

* Note for Cases Using Silica as Primary Analogue: For LOAEL doses, the Agency 

considers a margin of exposure (MOE) of 1,000 or greater as representing a low order of toxicity 

for health endpoints for which a threshold dose is deemed appropriate. In this instance, 

exposures would have to be reduced to 0.0007 mg/m3

 to achieve a MOE of 1,000, a 

concentration that is practically impossible to achieve. Because the LOAEL of 0.74 mg/m3

 is 

based on test data on pure silica and because silica is considered to be a much more potent lung 

toxicant than crystalline particulates containing silica, the Agency has adopted the NIOSH 

REL (Recommended Exposure Limit) for silica, 0.05 mg/m3, as a NCEL (New Chemical 

Exposure Limit ) - see http://www.epa.gov/opptintr/newchems/pubs/ncelmain.htm

for more information) concentration that would adequately protect workers from 

crystalline particulates containing silica. This NCEL replaces the former one based on the 

OSHA Permissible Exposure Limit (PEL) for silica, 0.1 mg/m3

. 

2. Fibrogenicity/Carcinogenicity of Talc

Humans. Epidemiology studies suggest an association between nonfibrous talc (a finely 

powdered hydrous magnesium silicate) and lung cancer risk. The OSHA PEL for talc is 20 

mppcf (million particles per cubic foot), and the NIOSH-recommended 8-hr TWA concentration 

is 2 mg/m3. 

Animals. In an NTP inhalation study (NTP TR 421, 1993), male and female F344 rats were 

exposed to 0, 6, or 18 mg/m3 talc for 113 and 122 weeks, respectively. There was clear 

evidence of the carcinogenicity of talc in female rats based on the increased incidence of 

alveolar/bronchiolar adenomas and carcinomas of the lung in the 18-mg/m3

 group (LOAEL). 

The No Observed Adverse Effect Level (NOAEL) from this study is 6 mg/m3

. The NCEL for 

analogous particulates would be 0.06 mg/m3

. 

3. Fibrogenicity/Carcinogenicity of Titanium Dioxide (TI)

Humans. According to IARC (ACGIH 1993), there is inadequate evidence for the 

carcinogenicity of TI in humans. [There is limited evidence for the carcinogenicity of TI in 

experimental animals.] Overall evaluation: TI is not classifiable as to its carcinogenicity to 

humans. The OSHA PEL=s for nuisance dust (in which TI is included) are 15 mg/m3

 total 

particulates and 5 mg/m3

 respirable fraction. The ACGIH TLV-TWA is 10 mg/m3 of total dust 
123 

containing no asbestos and <1% crystalline silica. 

The various literature case reports of lung toxicity in TI-exposed workers are generally 

inconclusive because of several factors--smoking; other conditions, such as tuberculosis; or 

incomplete data on TI exposure histories. 

In one fairly comprehensive cohort study, Chen and Fayerweather (1988, as summarized in 

ACGIH 1993) analyzed lung cancer mortality and incidence of chronic respiratory disease, chest 

x-ray abnormality, and pulmonary fibrosis among 1,576 workers exposed to TI for at least 1 yr at 

two production facilities between 1935 and 1984. Of the 211 deaths, 14 were attributed to 

respiratory cancer and 11 to nonmalignant respiratory disease compared with 18.3 and 13.8 cases 

expected, respectively, based on US mortality data. Expected deaths based on company 

mortality data since 1957 were 16.6 from respiratory cancer and 8.3 from nonmalignant 

respiratory disease. The authors concluded that the increase in deaths from nonmalignant 

respiratory disease compared with company data was not statistically significant. They further 

concluded that there was no significant association between exposure to TI and the respiratory 

diseases studied. 

Animals. There is limited evidence for the carcinogenicity of TI in experimental animals. 

Two-year inhalation studies in animals are summarized below. 

(1) Lee et al. (1986, as cited in ACGIH 1993 and in USEPA 1983) exposed Charles River-CD 

rats to 0, 10, 50, or 250 mg/m3

 for 6 hr/day 5 days/wk for 2 yr. The mean respirable fractions 

were 93.7% or greater. Squamous cell carcinomas developed after exposure to the highest 

dose for the full 2 yr. The authors considered the carcinomas to be unique, experimentally 

induced tumors in rats and to be of questionable relevance to humans. Given the amount of 

dust in the rat lungs, the tumors were postulated to be the result of saturation of normal 

pulmonary clearance mechanisms. There were minute areas of lung fibrosis at the two higher 

exposure levels. 

At 50 mg/m3

, massive accumulations of dust-laden macrophages, foamy dust cells, and free 

particles were considered indicative of such an overload. At 10 mg/m3

, the architecture of the 

air spaces remained intact and there was no significant formation of scar tissue. The NOAEL is 

10 mg/m3

. 

(2) Heinrich et al. (1995, abstract only) exposed Wistar rats to diesel engine exhaust, carbon 

black, or ultrafine TI for 2 yr. Particle exposure concentrations were increased during the 

course of the experiment. The average particle concentration of TI was 10 mg/m3

. Lung 

tumor rates (not given) increased with increasing cumulative particle exposure times, 

independent of the type of particle. 

(3) Trochimowicz et al. (1988, abstract only) exposed Charles River-CD rats to 10, 50, or 250 

mg/m3

 TI for 6 hr/day, 5 days/wk for 104 wk. Microscopic findings included alveolar cell 

hyperplasia, dust deposition, and minute areas of collagen fiber deposition associated with 

cholesterol giant cell granulomas. The earliest indicator of TI exposure was alveolar cell 
124 

hyperplasia. Lung tumors were only found in rats exposed to 250 mg/m3

. The NOAEL from 

this study is 10 mg/m3

. 

On the basis of the NOAELs from the above studies, the NCEL for analogous particulates would 

be 0.1 mg/m3. However, this would make the NCEL for TI analogues identical to the OSHA 

PEL for silica, a highly potent lung toxicant that IARC (1997) has classified as a Group 1 

carcinogen in humans (see section 1, above). Therefore, it was decided to use the OSHA PEL 

for TI, which is 5 mg/m3

 (respirable fraction), as the NCEL for TI analogues. 

4. Lung Toxicity of PMN 96-175, Lithium Manganese Oxide

Animal Data Only. Rats were exposed by inhalation to 0 (air controls), 1, 4, or 16 mg/m3 of the 

PMN substance 6 hr/day, 5 days/wk for 90 days. At the highest concentration, rats developed 

inflammation of the lung and larynx. Similar results were seen in the 14-day range-finding 

study at concentrations ranging from 10 to 100 mg/m3

. The NOAEL from this study is 4 

mg/m3

. The NCEL for analogous particulates would be 0.04 mg/m3. 

5. Fibrogenicity/Carcinogenicity of Carbon Black

Chronic inhalation of carbon black produced pulmonary inflammation, fibrosis, and lung tumors 

in rats (Nikula et al. 1995, Heinrich et al. 1995). These effects were observed at dust 

concentrations of 2.5, 6.6, and approximately 10 mg/m3

 carbon black. The LOAEL from these 

studies is 2.5 mg/m3. The NCEL for analogous particulates would be 0.0025 mg/m3. [The 

OSHA PEL for carbon black is 3.5 mg/m3

.] 

General Testing Strategy

A 90-day inhalation toxicity test (Harmonized Test Guideline 870.3465) in rats with special 

attention to histopathology (inflammation and cell proliferation) of the lung tissues and to 

various parameters of the bronchoalveolar lavage fluid (BALF), e.g., marker enzyme activities, 

total protein content, total cell count, cell differential, and cell viability. It is not necessary to 

look at internal organs. It is recommended that a recovery period of 60 days be included to assess 

the progression or regression of any lesions. If the results of the subchronic study indicate that 

the PMN particles have carcinogenic potential, a 2-year inhalation bioassay in rats may be 

warranted. 

REFERENCES

ACGIH. 1993. American Conference of Governmental Industrial Hygienists: Threshold 

Limit Values for Chemical Substances and Physical Agents and Biological Exposure Indices, 

1993-1994. Cincinnati, Ohio: ACGIH. 

Heinrich U, Fuhst R, Rittinghausen S, Creutzenberg O, Bellmann B et al. 1995. Chronic 

inhalation exposure of Wistar rats and two different strains of mice to diesel engine exhaust, 

carbon black, and titanium dioxide. Inhal Toxicol 7:533-556. Abstract only. 
125 

Holland LM. Reg. Toxicol. Pharmacol. 12:224-237, 1990 

IARC. 1997. International Agency for Research on Cancer. Monographs. Vol. 68, 

pp.41-336. 

ILSI. 2000. International Life Sciences Institute. Workshop: The relevance of the rat lung 

response to particle overload for human risk assessment. Inhal Toxicol 12: 1-17. 

Nikula KJ, Snipes MB, Griffith WC, Henderson RF, Mauderly JL. 1995. Comparative 

pulmonary toxicities and carcinogenicities of chronically inhaled diesel exhaust and carbon 

black in F344 rats. Fund Appl Toxicol 25:80-94. 

NTP. Toxicology and Carcinogenesis Studies of Talc in F334/N rats and B6C3F1 mice. National 

Toxicology Program, Technical Report No. 421, 1993. 

Trochimowicz HJ et al. 1988. J Appl Toxicol 8:383-435. Abstract only. 

USEPA. 1983. Status report for 8EHQ-1083-0497. Preliminary findings from a 2-yr rat 

inhalation study of titanium dioxide conducted by E.I. Du Pont de Nemours & Co., Inc. From 

Justine Welch, Chief, Chemical Risk Indentification Section, to Frank Kover, Chief, Chemical 

Screening Branch, Existing Chemicals Assessment Div., OPPT, USEPA. 

Woo, Y.-T., Lai, D.Y., Arcos, J.C., and Argus, M.F.: Chemical Induction of Cancer, Vol. III C, 

Academic Press, p. 508, 1988. 

October, 2002 
126 

Category: Rosin Environmental Toxicity 

Definition. This category includes rosin, abietic acid, abietinic acid, sylvic acid, their salts, and 

polymeric forms whose MW < 1000. The mode of toxic action of rosin is unknown. It is 

assumed that these compounds need to be absorbed to be toxic, therefore, compounds with MWs 

> 1000 will be excluded from this category. It is also assumed that these compounds need to 

be water soluble to be toxic, therefore, compounds with water solubilities (WS) < 0.001 mg/L 

(ppm) will also be excluded from this category. 

Hazard Concerns. The acute toxicity for rosin towards fish has been measured to be between 

0.410 to 0.700 mg/L by Leach and Thakore (1976 and 1978). Toxicity to aquatic invertebrates 

and green algae have no been reported. Based on these data, rosin presents a high concern for 

toxicity towards the aquatic environment. 

Boundaries. The only lower boundary is water solubility which is set at 0.001 mg/L (ppm). 

The only upper boundary will be set at a MW > 1000 for stable compounds. The 

environmental base set of tests will be requested for aquatic releases and the terrestrial base set 

of tests will be recommended for terrestrial exposures. 

General Testing Strategy. 

The aquatic base set of environmental toxicity tests will be recommended for aquatic exposures. 

The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients (AI) 

and mean measured concentrations; measured TOC of dilution water in the control; the highest 

treatment concentration on a nominal-basis should equal the aqueous solubility limit; and solvent 

can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with static 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at 24, 48, 

72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final concentration; the 

highest treatment concentration on a nominal-basis equal to the aqueous solubility limit; and 

solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be 

used to artificially enhance the water solubility. 

Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing (Harmonized Test 

Guideline 850.1400), with flow-through methods; measured concentrations; effective 

concentrations based on 100% active ingredients (AI) and mean measured concentrations; 

statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured TOC of 

dilution water in the control; the highest treatment concentration on a nominal-basis should be 

set at the aqueous solubility limit; solvent can be used to assist the PMN to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility; and the 
127 

7-d ELS stage toxicity test cannot be substituted for the 28-d ELS toxicity test because Van 

Leeuwen et al (1990) have demonstrated that the 7-d ELS toxicity test underestimated the 

chronic toxicity of anilines measured by the 28-d ELS toxicity test by >5.3 times when the 

NOECs were compared (see Table VII in Van Leeuwen); 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; the highest treatment concentration 

on a nominal-basis should be set at the aqueous solubility limit; solvent can be used to assist the 

PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the 

water solubility; and the 7-d daphnid chronic toxicity test cannot be substituted for the 21-d 

toxicity test because Van Leeuwen et al (1990) have demonstrated that the fish 7-d ELS toxicity 

test underestimated the chronic toxicity of anilines measured by the fish 28-d ELS toxicity test 

by >5.3 times when the NOECs were compared (see Table VII in Van Leeuwen). 

The terrestrial base set of environmental toxicity tests (i.e., the early seeding growth test, 

Harmonized Test Guideline 850.4230), the earthworm acute toxicity test (Harmonized Test 

Guideline 850.6200), and the soil microbial community bioassay (Test Guideline 850.5100) will 

be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial organisms 

include: the plant whole life cycle test (Test Guideline 850.4150), the plant uptake test (Test 

Guideline 850.4800), and the soil microbial community bioassay (Test Guideline 850.5100). 

References.

Leach , J. M. and Thakore, A. N., 1976. Toxic constituent in mechanical pulping effluents. 

Tappi, 59:129. 

Leach , J. M. and Thakore, A. N., 1978. Compounds toxic to fish in pulp mill waste streams. 

Progr. Water Technol. (G.B.) 9:787. 

Van Leeuwen CJ, Adema DMM, and Hermens J. 1990. Quantitative structure-activity 

relationships for fish early life stage toxicity. Aquatic Toxicology 16:321-334. 

January, 1994; revised June 2010 
128 

Category: Stilbene, derivatives of 4,4-bis(triazin-2-ylamino)-

Human Health (case-by-case) 

Definition. Any water soluble (sulfonated) derivative of 4,4-bis(triazin-2-ylamino) stilbene is 

considered to be a member of this category.

Hazard Concerns. EPA previously identified hazard concerns for the possible 

developmental/reproductive toxicity of new chemicals falling into this stilbene, derivatives of 

4,4-bis(triazin-2-ylamino)- category based on published test results for a member of the category. 

EPA has reviewed test data developed by the Stilbene Whitening Agent Task Force of the 

Ecological and Toxicological Association of Dyes and Organic Pigments Manufacturers (ETAD). 

These studies consisted of a range-finding and definitive 2-generation rat study (gavage) and 

range-finding and definitive developmental toxicity studies in rats and rabbits (gavage) for C.I. 

Fluorescent Brightener 220 (CAS No. 16470-24-9). Based on the results from these studies, 

EPA has concluded that available information does not support continued identification of 

stilbenes as a new chemical category presenting concerns for possible 

developmental/reproductive toxicity. EPA will continue to evaluate the potential health 

concerns for new chemical stilbenes that are notified but, with this change, will not apply a 

category understanding as regards potential developmental/reproductive toxicity. 

References.

Breslin, WJ. A pilot prenatal developmental toxicity study of C.I. Fluorescent Brightener 220 

and C.I. Fluorescent Brightener 339 administered via oral gavage to rats. MPI Research 

Laboratory Study Identification 795-001, August 18, 1998a. 

Breslin, WJ. A pilot prenatal developmental toxicity study of C.I. Fluorescent Brightener 220 

and C.I. Fluorescent Brightener 339 administered via oral gavage to New Zealand White rabbits. 

MPI Research Laboratory Study Identification 795-002, August 18, 1998b. 
129 

Turck, PA. Prenatal developmental toxicity study of C.I. Fluorescent Brightener 220 

administered via oral gavage to rats. MPI Research Laboratory Study Identification 795-003, 

December 2, 1999. 

Turck, PA. Range-finding reproduction study of C.I. Fluorescent Brightener 220 administered 

via oral gavage to rats. MPI Research Laboratory Study Identification 795-005, June 8, 2000a. 

Turck, PA. Prenatal developmental toxicity study of C.I. Fluorescent Brightener 220 

administered via oral gavage to New Zealand White rabbits. MPI Research Laboratory Study 

Identification 795-004, January 27, 2000b. 

Turck, PA. Two generation reproduction and fertility study of C.I. Fluorescent Brightener 220 

administered via oral gavage in rats. MPI Research Laboratory Study Identification No. 

795-006, August 24, 2001. 

Previous Category Statement References.

Burg, AW, Rohovsky, MW & Kensler, CJ (1977). Current status of human safety and 

environmental aspects of fluorescent whitening agents used in detergents in the United States. 

Critical Review & Environmental Control, 7, 91-120. 

Gloxhuber, CH & Bloching, H (1978). Toxicologic properties of fluorescent whitening agents. 

Clinical Toxicology, 13, (2), 171-203. 

Keplinger, ML, Fancher, OE, Lyman, FL & Calandra, JC (1974). Toxicologic studies of four 

fluorescent whitening agents. Toxicology & Applied Pharmacology, 27, 494-506. 

Keplinger, ML, Lyman, FL & Calandra, JC (1975). Three-generation reproduction studies with 

FWAs. In: Flourescent Whitening Agents. R. Anliker & G. Muller (Eds.). Stuttgart, 

Germany: Georg Thieme Publishers. 

Kramer, JB (1992). Fluorescent whitening agents. In: The Handbook of Environmental 

Chemistry, 3, (part F), 351-366. O. Hutzinger (Ed.). Heidelberg, Germany: Springer-Verlag 

Berlin. 

Lorke, D (1975). Studies of embryo toxicity in rats & rabbits. In: Flourescent Whitening 

Agents. R. Anliker & G. Muller (Eds.). Stuttgart, Germany: Georg Thieme Publishers. 

Lyman, FL, Schulze, J, Ganz, CR, Stensby, PS, Keplinger, ML & Calandra, JC (1975). 

Long-term toxicity of four fluorescent whitening agents. Food, Cosmetics & Toxicology, 13,

521-527. 

Poiger, T & Giger, W (1991). Determination of fluorescent whitening agents in sewage and 

sewage sludge by high performance liquid chromatography. Reprint of a poster presented at 

the meeting of the Swiss Chemical Society in Bern, Switzerland. October 18, 1991. 
130 

EAWAG/ETH, CH-8600 Dubendorf, Switzerland. 

Zinkernagel, R (1975). Fluorescent whitening agents in the environment. In: Flourescent 

Whitening Agents. R. Anliker & G. Muller (Eds.). Stuttgart, Germany: Georg Thieme 

Publishers. 

8E-CAP - 0024. Report to Ciba-Geigy Corporation. Teratogenic study with FA-15 in Albino 

rabbits, May 23, 1972. Submitted to USEPA on October 9, 1992. 

PB81-148819. Information Hazard Profiles on Potential Occupational Hazards. Vol. 2. 

Chemical Classes Fluorescent Whitening Agent (FWA's). National Institute for Occupational 

Safety and Hazard, Rockville, Maryland. December 1979. 

January, 1992; revised December, 1994; revised August, 2002. 
131 

Category: Thiols Environmental Toxicity 

Definition. This category includes all thiols or mercaptans. It is assumed that thiols have to 

be absorbed to be toxic, therefore, compounds with MWs > 1000 will be excluded from this 

category. Acute toxicity for thiols which are liquids at room temperature is known to be 

limited by the octanol/water partition coefficient (Kow). Above a log Kow value ≥6.5, thiols 

show no effects at saturation during 96-h exposures for fish. The log Kow cut-offs for other 

organisms for acute effects are generally lower. Thiols which are solids at room temperature 

may show no toxicity at saturation at lower Kow values depending on the melting point, i.e., the 

higher the melting point at a given Kow, the greater the likelihood that no toxicity will be 

observed at saturation. For solids, the no effects at saturation has to be determined on a 

case-by-case basis. There are no known Kow limits for chronic toxicity at this time, but it may 

not be much above a log Kow of 8 to 9 for liquid thiols. 

Hazard Concerns. The aquatic toxicity for thiols and mercaptans has been determined 

through SAR analysis by EPA using ECOSAR – a hazard estimation tool that uses chemical 

structure descriptors to estimate the acute and chronic toxicity of a substance to aquatic 

organisms. [Link for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

Thiols which are substituted with a carboxylic acid will be about 10 times less toxic than 

predicted by this SAR at pH 7. Use the Kow for the free acid. 

Members of this category exhibit toxicity ranging from low toxicity (i.e., > 100 mg/L) to high 

toxicity (i.e., < 1 mg/L) depending on their Kow, MW and substitutions. 

Boundaries. There are no known lower boundaries. The upper boundaries will be based on 

Kow and MW. Acute toxicity expected with log Kow <6.5 for fish; no effects at saturation 

during 96-h exposures when log Kow >6.5 for fish. Chronic toxicity has no known upper bound 

for log Kow, but it is probably near 9. MW will be <1000. The environmental base set of tests 

will be requested for aquatic releases and the terrestrial base set of tests will be recommended for 

terrestrial exposures. When the log Kow is >6.5, chronic toxicity testing will be recommended. 

General Testing Strategy

I. Release to Aquatic Ecosystems

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations; effective concentrations will be based on 100% active ingredients 

(AI) and mean measured concentrations; measured TOC of dilution water in the control; the 

highest treatment concentration on a nominal-basis should equal the aqueous solubility limit; and 

solvent can be used to assist the PMN to reach its aqueous solubility limit quicker, but cannot be 

used to artificially enhance the water solubility of the PMN beyond its aqueous solubility limit. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 
132 

static methods; measured concentrations; effective concentrations based on 100% active 

ingredients (AI) and mean measured concentrations; statistical analysis of effective 

concentrations at 24, 48, 72, and 96 hours; test medium with at least 0.300 mg/L EDTA as a final 

concentration; the highest treatment concentration on a nominal-basis equal to the aqueous 

solubility limit; and solvent can be used to assist the PMN to reach its aqueous solubility limit 

quicker, but cannot be used to artificially enhance the water solubility of the PMN beyond its 

aqueous solubility limit. 

If there is no significant risk from the PMN after the results of the environmental base set have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 2. 

Tier 2. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

 -Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

If there is no significant risk from the PMN after the results of the aerobic biodegradation have 

been integrated into the risk assessment, then no further testing is recommended. However, if 

there is a significant risk, then go to Tier 3. 

Tier 3. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with flow-through methods; measured concentrations; 

effective concentrations based on 100% active ingredients (AI) and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, 21, and 28; measured 

TOC of dilution water in the control; the highest treatment concentration on a nominal-basis 

should be set at the aqueous solubility limit; solvent can be used to assist the PMN to reach its 

aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility of 

the PMN beyond its aqueous solubility limit; and the 7-d ELS stage toxicity test cannot be 

substituted for the 28-d ELS toxicity test. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21; measured TOC of dilution water in the control; the highest treatment concentration 

on a nominal-basis should be set at the aqueous solubility limit; solvent can be used to assist the 

PMN to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the 

water solubility of the PMN beyond its aqueous solubility limit; and the 7-d daphnid chronic 

toxicity test cannot be substituted for the 21-d toxicity test. 

II. Release to Terrestrial Ecosystems

The terrestrial base set of environmental toxicity tests (i.e., the early seeding growth test, 

Harmonized Test Guideline 850.4230), the earthworm acute toxicity test (Harmonized Test 
133 

Guideline 850.6200), and the soil microbial community bioassay (Test Guideline 850.5100) will 

be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial organisms 

include: the plant whole life cycle test (Test Guideline 850.4150), the plant uptake test (Test 

Guideline 850.4800), and the soil microbial community bioassay (Test Guideline 850.5100). 

December, 1994; revised June 2010 
134 

Category: Substituted Triazines Environmental Toxicity 

Definition. This category includes substituted triazines which can be aromatic, partially 

aromatic (or partially saturated) and unsaturated. The nitrogens in the triazine ring may be 

symmetrical or asymmetrical. Substitutions on the carbons may include but not be limited to: 

aliphatic alcohols; ketones; benzene and substituted benzenes; aliphatic hydrocarbons, 

alkyenes and alkynes; free amines and substituted amines; cyclic aliphatic hydrocarbons; 

halogens; amides; cyanides; ethers; methoxy groups; sulfides; azido groups; and carboxylic acid 

esters. Substitutions on the nitrogens may include but not be limited to: free amines and 

substituted amines; -N=CH; aliphatic hydrocarbons, alkyenes and alkynes; and benzene and 

substituted benzenes. 

Hazard Concerns. Many members of this category are commercial herbicides which are used 

to control both aquatic plants and terrestrial plants. Their mode of toxic action is generally 

considered to be inhibition of photosynthesis. Many members of this class are toxic to algae at 

< 1 mg/L and toxic to terrestrial vascular plants at < 1 mg/kg. Members of this group can also be 

highly toxic to fish and aquatic invertebrates. Toxicity is expected to be related to the 

octanol/water partition coefficient with respect to fish and aquatic invertebrates, but toxicity to 

plants may not be related to Kow when log Kow < 5. When the log Kow is < 5, algae and 

terrestrial plants are expected to be the most sensitive species. As log Kow increases, species 

differences are expected to diminish. The aquatic toxicity substituted triazines has been 

determined through SAR analysis by EPA using ECOSAR – a hazard estimation tool that uses 

chemical structure descriptors to estimate the acute and chronic toxicity of a substance to aquatic 

organisms. [Link for ECOSAR: http://www.epa.gov/opptintr/newchems/tools/21ecosar.htm]. 

Boundaries. There are no known lower boundaries. The upper boundaries are based on Kow 

and MW. When the log Kow value is < 5 mg/L, the environmental base set of tests will be 

requested for aquatic releases and the terrestrial base set of tests will be recommended for 

terrestrial exposures. When the log Kow is between 5 and 8, only chronic toxicity testing will 

be recommended. When the log Kow is > 8, no testing will be requested because no toxic 

effects at saturation will be expected. Generally, members of this category will have MWs of 

less than 1000. 

General Testing Strategy 

The aquatic base set of environmental toxicity tests will be recommended for aquatic exposures 

and the terrestrial base set of environmental toxicity tests (i.e., the early seedling growth test, the 

earthworm acute toxicity test and the soil microbial community bioassay) will be recommended 

for terrestrial exposures. 

August, 1989; revised June 2010 
135 

Category: Triarylmethane Pigments/Dyes

 with Non-solubilizing Groups Human Health 

Environmental Toxicity 

Other Names: Triphenylmethane Pigments/Dyes, Diphenylnaphthyl-methane Pigments/Dyes 

Definition. Structurally, triarylmethane pigments/dyes are derivatives of triphenylmethane or 

diphenylnaphthylmethane. In order to achieve the required spectral absorption properties that 

characterize these dyes, amine groups (primary, secondary, or tertiary) or hydroxyl groups must 

be present on the aromatic ring positions para to the methane carbon. Amine substitutions are 

more prevalent than hydroxy substitutions (C.I. 42000-42175 for diamino derivatives, C.I. 

42500-42800 for triamino derivatives, C.I. 43800-43875 for hydroxy derivatives, and 

43500-43570 for aminohydroxy derivatives. 

Hazard Concerns. There are oncogenicity concerns for the triarylmethane pigments/dyes 

based on analogy to Gentian Violet and C.I. Basic Red 9. In addition, there are developmental 

and reproductive toxicity concerns for these compounds based on analogy to Gentian Violet and 

Malachite Green. Ecotoxicity concerns are based on QSAR predictions for delocalized cationic 

dyes. Cationic dyes are an established ecotoxicity category. 
136 

Boundaries. Pigments/Dyes included in this category are the di- and tri-amino substituted 

triphenylmethane and diphenylnaphthyl-methane derivatives. Dyes substituted with 

solubilizing groups such as carboxylic acid, sulfonic acid, or halogens, are not included. 

Pigments that have essentially negligible water solubility (<1ppb) and therefore, little or no 

bioavailability, are also not included. 

General Testing Strategy 

The New Chemicals Program considers the following tests to be appropriate to address the 

potential for triarylmethane pigments/dyes to pose a significant risk. 

I. Health 

- Developmental toxicity study in two species of rodents by the oral route (Harmonized 

Test Guideline 870.3700). 

- Two-generation reproductive toxicity study in rodents by the oral route (Harmonized 

Test Guideline 870.3800). 

- Salmonella typhimurium/Ames assay with the Chinese hamster liver S9 activation 

system (Harmonized Test Guideline 870.5100). 

- In vivo mouse micronucleus assay i.p. (Harmonized Test Guideline 870.5395). 

Tests 3. and 4. would trigger a lifetime rodent bioassay if positive. 

II. Environmental Toxicity and Fate 

Prior to Tier 1, first the following physical-chemical properties need to be established: 

- Melting point (Harmonized Test Guideline 830.7200) or boiling point (Harmonized 

Test Guideline 830.7220) 

- Water solubility (Harmonized Test Guideline 830.7840 or 830.7860) 

- Log Kow (Harmonized Test Guideline 830.7550, 830.7560, or 830.7570; or OECD 123, 

Partition Coefficient (1-Octanol/Water): Slow-Stirring Method) 

- Vapor pressure (Harmonized Test Guideline 830.7950). 

Tier 1. The fish, daphnid, and algal (Harmonized Test Guideline 850.5400) acute toxicity tests 

from the aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method with 

measured concentrations, and effective concentrations will be based on 100% active ingredients 

(AI) and mean measured concentrations. 
137 

If there is no significant risk from the PMN after the results of the fish and daphnid acute toxicity 

tests have been integrated into the risk assessment, then no further testing is recommended. 

However, if there is a significant risk, then go to Tier 2. 

Tier 2. Phototransformation of Chemicals in Water— Indirect Photolysis Screening Test 

(Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 3; if t1/2 > 2 days, then 

integrate the results into the risk assessment. If there is no significant risk from the PMN, then 

no further testing is recommended. However, if there remains a significant risk, then go to Tier 

4. 

Tier 3a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental risk. If there is no significant risk from the photolysis 

products from the PMN, then no further testing is recommended. However, if there remains a 

significant risk, then go to Tier 4. 

Tier 3b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then prepare 

a stock solution of PMN using the standard humic-containing solution described in the 

photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test photolysis products for 

toxicity with most sensitive species from environmental base set. For example, if the most 

sensitive species from the environmental base set has an EC50 value = 2.0 mg/L (based on 100% 

active ingredients [AI]), then prepare a 5.0 mg PMN per liter stock solution based on 100% AI 

using the standard humic-containing solution. This stock solution is exposed to sunlight for at 

least 6 half-lives to ensure that all of the PMN has been photolyzed, and then this stock solution 

is used to retest the most sensitive aquatic species to determine if the photolysis products of the 

PMN are more or less toxic that the PMN. Integrate these toxicity results into the risk 

assessment. If there is no significant risk from the PMN, then no further testing is 

recommended. However, if there remains a significant risk, then go to Tier 4. 

Tier 4. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test Guideline 

835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized Test 

Guideline 835.3140) 

Integrate the results for aerobic biodegradability into the risk assessment. If there is no 

significant risk from the PMN, then no further testing is recommended. However, if there 

remains a significant risk, then do chronic toxicity testing for fish and daphnids: 

Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing (Harmonized Test 

Guideline 850.1400), with flow-through methods; measured concentrations; effective 

concentrations based on 100% active ingredients (AI) and mean measured concentrations; and 

statistical analysis of effective concentrations at days 7, 14, 21, and 28. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with flow-through 
138 

methods; measured concentrations; effective concentrations based on 100% active ingredients 

(AI) and mean measured concentrations; statistical analysis of effective concentrations at days 7, 

14, and 21. 

For Terrestrial ecosystemsThe terrestrial base set of environmental toxicity tests (i.e., the early seeding growth test, 

Harmonized Test Guideline 850.4230), the earthworm acute toxicity test (Harmonized Test 

Guideline 850.6200), and the soil microbial community bioassay (Test Guideline 850.5100) will 

be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial organisms 

include: the plant whole life cycle test (Test Guideline 850.4150), the plant uptake test (Test 

Guideline 850.4800), and the soil microbial community bioassay (Test Guideline 850.5100). 

References:

American Dye Manufacturers Institute, Inc. (ADMI), 1974, "Dyes and the Environment: 

Reports on Selected Dyes and Their Effects," Vol. II, ADMI, New York. 

Au W, Pathak S, Colie CJ, Hsu TC. 1978. Cytogenetic toxicity of Gentian Violet and Crystal 

Violet on mammalian cells in vitro. Mutation Research 58:269-276. 

Au W, Butler MA, Bloom SE, Matney TS. 1979. Further study of the genetic toxicity of Gentian 

Violet. Mutation Research 66:103-112. 

Auer, C. M., Nabholz, J. V. and Baetcke, K. P., 1990, "Mode of Action and the Assessment of 

Chemical Hazards in the Presence of Limited Data: Use of Structure-Activity Relationships 

(SAR) under TSCA, Section 5," Environmental Health Perspectives, Vol. 87, pp. 183-197. 

Kier LD, Brusick DJ, Auletta AE. 1986. The Salmonella typhimurium/mammalian microsomal 

assay. A report of the U.S. Environmental Protection Agency Gene-Tox Program. Mutation 

Research 168:69-240. 

Kirk-Othmer, Encyclopedia of Chemical Technology, 3rd edition, vol. 23, pages 399-412. 

Little, L. W. and Lamb J. C., III, 1972. Acute Toxicity of 46 Selected Dyes to the Fathead 

Minnow, Pimephales promelas,Final Report to the American Dye Manufacturers Institute,Inc., 

UNC Wastewater Research Center, Department of Environmental Sciences and Engineering, 

School of Public Health, University of North Carolina, Chapel Hill, NC. 

Littlefield NA, Blackwell B-N, Hewitt CC, Gaylor DW. 1985. Chronic toxicity and 

carcinogenicity studies of Gentian Violet in mice. Fundamental and Applied Toxicology

5:902-912. 

Mortelmans K, Haworth S, Lawlor T. 1986. Salmonella mutagenicity tests: II. Results from the 

testing of 270 chemicals. Environmental Mutagenesis 8(7):1-119. 
139 

Nabholz, J. V., 1990. The OTS PMN ECOTOX Data Base: a Confidential Business Information 

(CBI) Collection of Environmental Toxicity Data from New Chemical Submissions Under Sec. 5. 

Unpublished, Environmental Effects Branch, Health and Environmental Review Division 

(TS-796), U. S. Environmental Protection Agency, Washington, DC. 

NCTR Technical Report for Experiment Numbers 305,354,355. Three-generation reproduction 

and toxicity studies of Gentian Violet in Fischer 344 Rats. National Center for Toxicological 

Research. Jefferson, Arkansas. Sept. 1988. 

NCTR Technical Report for Experiment Number 355. Developmental toxicity study of Gentian 

Violet in Fischer 344 Rats. National Center for Toxicological Research. Jefferson, Arkansas. 

Sept. 1988. 

NTP. 1985. National Toxicology Program. C.I. Basic Red 9 monochloride. NTP TR-285. 

Sigman, C. C., Helms, C. T., Papa, P. A., Atkinson, D. L., Doeltz, M. K. and Winship-Ball, A., 

Jan. 1983. Anthraquinone Dyes and Related Chemicals: Review and Assessment of Potential 

Environmental and Health Aspects. Final Report to the Dyes Environmental and Toxicology 

Organization, Inc., SRI International, Menlo Park, CA. 

Sokolowska-Pituchowa J, Kowalczkowa J, Kus J, Piotrowski J, Sawicki B. 1965. Teratogenic 

effect of Malachite Green in experimental animals. Folia Biologica 13:311-315. 

Tonogai, Y., Ito, Y., Iwaida, M., Tati, M., Ose, Y. and Sato, T., 1979. Studies on the Toxicity of 

Coal-Tar Dyes. II. Examination of the Biological Reaction of Coal-Tar Dyes to Vital Body. 

The Journal of Toxicological Sciences, Vol. 4, pp. 211-219. 

July, 1994; revised June 2010. 
140 

Category: Vinyl Esters Human Health 

Environmental Toxicity 

(See AEsters@) 

Definition: A carboxylic acid ester with at least one vinyl group (CH2=CH-) attached to an 

organic acid radical (RCOO-). A simple vinyl ester is vinyl acetate: 

 CH3COOCH=CH2

Note: Certain carboxylic acid moieties themselves may exert toxicity such that there are 

concerns for effects in addition to those identified for the vinyl ester class. 

Hazard Concerns: Oncogenicity based on data from two bioassays: a 2-yr drinking water 

study of vinyl acetate in rats [significantly increased incidences of adenocarcinomas of the uterus 

and combined C-cell adenomas and carcinomas in high-dose (2,500 mg/l) female rats] and a 

chronic inhalation study of vinyl acetate in rats and mice (laryngeal/nasal tumors in rats, 

bronchiolar/alveolar adenomas in lungs of mice). There are supporting data from 27-mo and 

81-wk inhalation studies of acetaldehyde in rats and hamsters, respectively. Furthermore, 

mutagenicity data on these analogues support a cancer concern. Neurotoxicity based on data on 

an analogous PMN compound in rats plus suggestive data on vinyl acetate. Reproductive 

toxicity based on a two-generation study of vinyl acetate in rats. Environmental toxicity (see 

"Esters" category). 

Boundaries. Other than a requirement for a vinyl group and an acid group, none. 

General Testing Strategy 

(1) Up-front glove permeation study if there is a risk of any toxicity through dermal exposure. 

(2) Hydrolysis test (both acid- and enzyme-catalyzed) to determine the rate at which 

acetaldehyde, a potentially toxic metabolite, is released. [The requirement to measure 

acetaldehyde release is based on the assumption that acetaldehyde is the presumed "ultimate 

carcinogen" of vinyl esters. This requirement will be revisited as more decisive data become 

available. The hydrolysis data should be helpful in determining the most appropriate route of 

administration in the following tests.] 

(3) A 90-day neurotoxicity test in rats that includes a functional observational battery, motor 

activity tests, and neuropathology examinations. Also to be included, to address reproductive 

toxicity concerns, are the following adjuncts to the subchronic test: 
141 

(a) Weights of the testes, epididymides (total and cauda), pituitary, seminal vesicles (with 

coagulating glands), prostate, ovary, and uterus are to be recorded at the time of sacrifice. 

(b) Histopathology of the testes is to be done on the males at the time of sacrifice. 

Particular attention is to be directed toward achieving satisfactory quality from fixation 

and embedding, and preparations are to follow the recommendations of Russell et al. 

(1990). Histologic analyses are to include evaluations of the spermatogenic cycle; i.e., 

the presence and integrity of the 14 cell states. These evaluations would follow the 

guidance provided by Russell et al. 

(4) A standard developmental toxicity study in rabbits and rats. 

(5) A 2-yr bioassay in rats and mice to address cancer concerns. 

(6) Environmental toxicity testing: see "Esters" category. 

References.

Russell LD, Ettlin RA, Sinha Hikim AP, Clegg ED. 1990. Histological and histopathological 

evaluation of the testis. Cache River Press, Clearwater, FL. 

August, 1992 
142 

Category: Vinyl Sulfones Human Health 

Environmental Toxicity 

Definition. Any molecular structure with a vinyl sulfone group is considered to be a member 

of the class: 

 O 

 ║

 -S-CH=CH2

 ║

 O 

In addition the following is an example of a functional group that generates a vinyl sulfone under 

certain conditions. β-Sulfatoethyl-sulfonyl groups are typical vinyl sulfone precursors. 

Structures bearing this group are also members of the class: 

 O 

 ║

 -S-CH2-CH2-OSO3

-

 ║

 O 

Typically, the new chemical of concern is a fiber-reactive dye bearing one or more vinyl 

sulfones, or vinyl sulfone precursors. Occupational exposure to workers via 

inhalation/ingestion of the powdered dye may pose a potential health risk. Under the 

conditions in a dye bath a vinyl sulfone precursor-containing dye generates the vinyl sulfone. 

In this scenario the only potential risk is to those who drink contaminated drinking water. 

However, following covalent binding of vinyl sulfone to textile fibers, survival of unbound vinyl 

sulfone substituents in the dye bath is low (< 10%). The majority of unbound vinyl sulfone is 

hydrolyzed to β-hydroxyethylsulfone. Unless releases to water are extremely high, vinyl 

sulfones are not expected to pose a significant risk to human health. Presently, there are no 

human health concerns for β-hydroxyethylsulfone. 

Hazard Concerns. For those who inhale or ingest a vinyl sulfone, there is an oncogenicity 

concern and mutagenicity concerns based on the potent mutagenicity of vinyl sulfone (VS) and 

methylvinyl sulfone (MVS). VS and MVS are mutagenic in the L5178Y TK+/- mouse 

lymphoma gene mutation assay in vitro. Evaluation of small colonies indicates that 

genotoxicity is due to a clastogenic mechanism. This is confirmed by evaluating the lymphoma 

cells for chromosome aberrations and micronuclei. MVS also induces effects upon the spindle 

apparatus in Chinese hamster lung cells in vitro, indicating an aneugenic (aneuploidy-inducing) 

activity. A direct-acting Michael addition-type reaction may be the mechanism of action. 

Although MVS and divinyl sulfone (DVS) are both reported as negative in vivo in the mouse 

micronucleus assay (inconclusive, only males tested), and in the dominant lethal assay, the 

Agency has determined that these negatives are not sufficient to remove concern for vinyl 

sulfone-containing new chemicals as potential mutagens and carcinogens. 
143 

There are ecotoxicity concerns for VS only, based on concerns for electrophiles. 

Boundaries. There are at present no boundary conditions, related to health effects, for 

structures containing vinyl sulfones. Nearly all new chemicals in the category have been 

water-soluble, fiber-reactive dyes with molecular weights <1,000. The boundary conditions for 

ecotoxicity effects are molecular weights < 1000 and log Kow < 8. 

General Testing Strategy 

The New Chemicals Program considers the following tests to be appropriate to address health 

and ecotoxicity concerns: 

1. Mouse lymphoma assay with evaluation of small colonies (Harmonized Test Guideline 

870.5300). The test would trigger a lifetime rodent bioassay if positive. 

2. Base-set ecotoxicity testing to include fish (Harmonized Test Guideline 850.1075), 

daphnids (Harmonized Test Guideline 850.1010) and algae (Harmonized Test Guideline 

850.5400). The acute toxicity tests for fish and daphnids will be done using the flow-through 

method with measured concentrations, and effective concentrations will be based on 100% 

active ingredients (AI) and mean measured concentrations. If there is insufficient knowledge 

about the water solubility of the dye, then it should also be measured (Harmonized Test 

Guideline 830.7840 or Harmonized Test Guideline 830.7860). 

If there is no significant risk from the PMN after the results of the fish and daphnid acute 

toxicity and algal toxicity tests have been integrated into the risk assessment, then no further 

testing is recommended. However, if there is a significant risk, then do environmental fate 

testing as outlined in 3. 

3. Environmental fate testing for releases to water: 

Tier 1. Phototransformation of Chemicals in Water— Indirect Photolysis Screening 

Test (Harmonized Test Guideline 835.5270). If t1/2 < 2 days, go to Tier 2; if t1/2 > 2 days, go to 

Tier 3. 

Tier 2a. If t1/2 < 2 days and photolysis products are known and/or identified, then assess 

photolysis products for environmental hazards. 

Tier 2b. If t1/2 < 2 days and photolysis products are not known and/or identifiable, then 

prepare a stock solution of the PMN chemical using the standard humic-containing solution 

described in the photolysis test, expose to sunlight for at least 6 half-lives (t1/2), and test 

photolysis products for toxicity with the most sensitive species from the environmental base set. 
144 

Tier 3. Aerobic biodegradability according to either of the following test guidelines: 

- Ready Biodegradability (six methods; choose any one) (Harmonized Test 

Guideline 835.3110) 

- Ready Biodegradability–CO2 in Sealed Vessels (Headspace Test) (Harmonized 

Test Guideline 835.3140) 

In addition, if appropriate, physical/chemical properties including: 

- Log Kow (Harmonized Test Guideline 830.7550, 830.7560, or 830.7570; or 

OECD 123, Partition Coefficient (1-Octanol/Water): Slow-Stirring Method) 

- Vapor pressure (Harmonized Test Guideline 830.7950) 

- Boiling point (Harmonized Test Guideline 830.7220) 

- Melting point range (Harmonized Test Guideline 830.7200) 

If the PMN chemical passes the aerobic biodegradability test according to the criteria set 

forth in the guidelines, no further testing may be recommended. A new risk assessment is 

conducted to determine if chronic ecotoxicity testing is warranted. 

4. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing (Harmonized 

Test Guideline 850.1400), with flow-through methods; measured concentrations; effective 

concentrations based on 100% AI and mean measured concentrations; and statistical analysis of 

effective concentrations at days 7, 14, 21, and 28. 

 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with 

flow-through methods; measured concentrations; effective concentrations based on 100% AI and 

mean measured concentrations; statistical analysis of effective concentrations at days 7, 14, and 

21. 

5. Ecotoxicity testing for release to terrestrial ecosystems. 

The terrestrial base set of environmental toxicity tests (i.e., the early seeding growth test, 

Harmonized Test Guideline 850.4230), the earthworm acute toxicity test (Harmonized Test 

Guideline 850.6200), and the soil microbial community bioassay (Test Guideline 850.5100) will 

be recommended for terrestrial exposures. Chronic toxicity testing for terrestrial organisms 

include: the plant whole life cycle test (Test Guideline 850.4150), the plant uptake test (Test 

Guideline 850.4800), and the soil microbial community bioassay (Test Guideline 850.5100). 

References:

Dearfield, KL, K Harrington-Brock, CL Doerr, JR Rabinowitz, and MM Moore (1991). 

Genotoxicity in mouse lymphoma cells of chemicals capable of Michael addition. Mutagenesis 

6: 519-525. 

Heyna, J (1963). Reactive dyes containing vinylsulfonyl groups. Angew. Chem. Internat. 
145 

Edit. 2(1): 20-23. 

Shelby, MD, GA Gutierrez-Espeleta, WM Generoso, and AF McFee (1991). Mouse dominant 

lethal and bone marrow micronucleus studies on methyl vinyl sulfone and divinyl sulfone. 

Mutation Research 250: 431-437. 

Warr, TJ, JM Parry, RD Callander, and J Ashby (1990). Methyl vinyl sulfone: A new class of 

Michael-type genotoxin. Mutation Research 245: 191-199. 

September, 1988; revised June, 1994; revised June 2010 
146 

Category: Soluble complexes of Zinc Environmental Toxicity 

Definition. This category includes all organic and inorganic soluble complexes of zinc, for 

example, zincates, organozincs, such as, dimethylzinc. Not included in this category are 

zinc-complexed acid dyes and strong ion pairs between zinc and anionic surfactants. There are 

no toxicity data for soluble complexes of zinc, therefore, the toxicity data for the free Zn++ ion 

will be used to predict aquatic toxicity. 

Hazard Concerns. Zinc produces acute toxicity to freshwater aquatic organisms over a range 

of concentrations from 90 to 58,100 ug/L and produces chronic toxicity over a range from 47 to 

852 ug/L. The acute to chronic ratio (ACR) for Zn has been set at 3 in the water quality criteria 

(WQC) document. Zinc concentrations from 30 to 21,600 ug/L have been shown to reduce the 

growth of various aquatic plants and algae appear to be the most sensitive group. 

Bioconcentration factors (as logarithms) for freshwater fish ranged from 1.7 to 2.6, and from 2.0 

to 3.1 for freshwater invertebrates. Zinc is an essential nutrient trace element which can be 

toxic at higher concentrations. While acute toxicity is affected by hardness, chronic toxicity is 

not affected. The freshwater criteria at an average hardness of 100 mg/L are 0.120 ug/L for 

acute exposures and 0.110 ug/L for chronic exposures; the saltwater criteria are 0.095 ug/L for 

acute exposures and 0.086 ug/L for chronic exposures. These criteria are based on toxicity 

information for the following Zn salts: sulfate, chloride, phosphate, and nitrate. 

General Testing Strategy 

To address ecotoxicity concerns, base set acute aquatic toxicity testing (algae: static method, 

daphnid and fish: flow-through method, all measured concentrations). 

April, 1990 
147 

Category: Zirconium Compounds Environmental Toxicity 

Definition. This category includes inorganic salts of zirconium (Zr), complexes between Zr 

and organic acids, and organoZr compounds, i.e., Zr covalently-bonded with carbon. For 

example, some inorganic Zr salts include: Zr sulfate, Zr oxychloride, and Zr tetrachloride. 

Not included in this category are dyes complexed with Zr. 

Hazard Concerns. Soluble salts of Zr are known to be moderately toxic to green algae and 

fish based on exposures in soft water and in terms of mg Zr/L. Toxicity information is only 

available for Zr sulfate, Zr tetrachloride, and Zr oxychloride. The toxicity profile for Zr based 

on available toxicity data, mg Zr/L (ppm Zr), and moderate hardness (i.e., 150.0 mg/L as CaCO3) 

is: 

Fish 96-h LC50 = 58.0 (n=3) 

Green algal 96-h EC50= 2.6 

Zirconium is more toxic in soft water than hard water. Acute toxicity to fish has been shown to 

increase 13 times as hardness decreases from 400.0 to 20 mg/L. 

Boundaries. The toxicity of Zr compounds depends on their physical/chemical properties and 

the hardness of receiving waters. The toxicity of Zr salts and Zr complexes with organic acids 

are expected to be related to their water solubility and MW. The toxicity of organoZr 

compounds are also expected to be related to their octanol/water partition coefficient (Kow). 

The most important property determining the toxicity of Zr compounds is water solubility. 

Water solubility cannot be estimated accurately and has to be measured. The water solubility 

of organoZr compounds is expected to decrease as Kow increases. There is no lower bound for 

Kow and the upper bound cannot be determined at this time since the Kow fragment-constant for 

Zr is not known. In addition to solubility, MW is also an important boundary. Compounds 

with MWs > 1000 are not expected to be absorbed by aquatic organisms even if they are water 

soluble. Therefore, only Zr compounds with MWs < 1000 are expected to be toxic. 

General Testing Strategy 

I. Release to Aquatic Ecosystems 

Tier 1. The aquatic base set of environmental toxicity tests will be recommended for aquatic 

exposures. The acute toxicity tests for fish (Harmonized Test Guideline 850.1075) and daphnids 

(Harmonized Test Guideline 850.1010) will be done using the flow-through method; effective 

concentrations will be based on 100% active ingredients (AI) and mean measured 

concentrations; the total organic carbon (TOC) concentration of dilution water in the control 

must be less than 2.0 mg TOC/L; TOC must be measured in the control just prior to the start of 

the test; the highest treatment concentration on a nominal-basis should not exceed the aqueous 

solubility limit of the tested compound; solvent can be used to assist the compound to reach its 
148 

aqueous solubility limit quicker, but cannot be used to artificially enhance the water solubility of 

the compound beyond its aqueous solubility limit; and hardness of dilution water has to be less 

than 180.0 mg/L as CaCO3. If toxicity mitigation testing is done with humic acid, then the 

static method with nominal concentrations will be recommended. 

The algal toxicity testing (Harmonized Test Guideline 850.5400), should be done with 

the static method; effective concentrations based on 100% AI and mean measured 

concentrations; statistical analysis of effective concentrations at 24, 48, 72, and 96 hours; test 

medium with no more than 0.300 mg/L EDTA as a final concentration; the TOC of the 

test/growth medium should be less than 2.0 mg TOC/L; TOC should be measured just prior to 

the start of the test; the highest treatment concentration on a nominal-basis should not exceed the 

aqueous solubility limit of the tested compound; and solvent can be used to assist the compound 

to reach its aqueous solubility limit quicker, but cannot be used to artificially enhance the water 

solubility of the compound beyond its aqueous solubility limit. If toxicity mitigation testing is 

done with humic acid, then nominal concentrations will be recommended. 

If there is no significant risk from the Zr compound after the results of the environmental 

base set have been integrated into the risk assessment, then no further testing will be 

recommended. However, if there is a significant risk, then go to Tier 2. 

Tier 2. Fish chronic toxicity testing, i.e., fish early life stage (ELS) toxicity testing 

(Harmonized Test Guideline 850.1400), with the flow-through method; effective concentrations 

based on 100% AI and mean measured concentrations; statistical analysis of effective 

concentrations at days 7, 14, 21, and 28; the TOC of dilution water in the control should be less 

than 2.0 mg TOC/L; TOC should be measured in the controls just prior to and during the test; the 

highest treatment concentration on a nominal-basis should not exceed the aqueous solubility 

limit of the tested compound; solvent can be used to assist the compound to reach its aqueous 

solubility limit quicker, but cannot be used to artificially enhance the water solubility of the 

compound beyond its aqueous solubility limit; and hardness of dilution water has to be less than 

180.0 mg/L as CaCO3. 

Daphnid chronic toxicity testing (Harmonized Test Guideline 850.1300), with the 

flow-through method; effective concentrations based on 100% AI and mean measured 

concentrations; statistical analysis of effective concentrations at days 7, 14, and 21; the TOC of 

dilution water in the control should not exceed 2.0 mg TOC/L; TOC must be measured in the 

controls just prior to and during the test; the highest treatment concentration on a nominal-basis 

should not exceed the aqueous solubility limit of the tested compound; solvent can be used to 

assist the compound to reach its aqueous solubility limit quicker, but cannot be used to 

artificially enhance the water solubility of the compound beyond its aqueous solubility limit; and 

hardness of dilution water has to be less than 180.0 mg/L as CaCO3. 

II. Release to Terrestrial Ecosystems: The terrestrial base set of environmental toxicity tests 

will be recommended for terrestrial exposures. The terrestrial base set includes: the early 

seeding growth test (Harmonized Test Guideline 850.4230), the earthworm toxicity test 

(Harmonized Test Guideline 850.6200), the soil microbial community bioassay (Harmonized 

Test Guideline 850.5100), and the avian acute oral toxicity test (Harmonized Test Guideline 

850.2100). Chronic toxicity testing for terrestrial organisms include: the plant whole life cycle 

test (Harmonized Test Guideline 850.4150), the plant uptake test (Harmonized Test Guideline 
149 

850.4800) and the avian reproduction test (Harmonized Test Guideline 850.2300). 

June, 1992; revised June 2010