For reasons of economy, this document is printed in a limited number. Delegates are 

kindly asked to bring their copies to meetings and not to request additional copies.

I:\MEPC\60\2-8.doc 

INTERNATIONAL MARITIME ORGANIZATION

IMO 

E

MARINE ENVIRONMENT PROTECTION 

COMMITTEE 

60th session 

Agenda item 2 

MEPC 60/2/8

26 August 2009

 Original: ENGLISH

HARMFUL AQUATIC ORGANISMS IN BALLAST WATER 

Application for Basic Approval of the OceanGuardTM Ballast Water ManagementSystem 

Submitted by Norway 

SUMMARY

Executive summary: This document contains non-confidential information for Basic 

Approval of the OceanGuardTM Ballast Water Management System 

under the “Procedure for approval of ballast water management 

systems that make use of Active Substances (G9)” adopted by 

resolution MEPC.169(57). The documentation complies with the 

requirements related to assessments for Basic Approval. 

Strategic direction: 7.1 

High-level action: 7.1.2 

Planned output: 7.1.2.4 

Action to be taken: Paragraph 5 

Related documents: BWM/CONF/36, MEPC 57/21 and BWM.2/Circ.18 

Introduction 

1 The Ballast Water Management Convention (BWM Convention), in regulation D-3.2, 

provides that ballast water management systems which make use of Active Substances to comply 

with the Convention shall be approved by the Organization. 

2 The “Procedure for approval of ballast water management systems that make use of 

Active Substances (G9)” identifies the information that should be included in a proposal for 

approval (MEPC 57/21, annex 4, paragraph 4.2.1) and provisions for risk characterization and 

analysis (MEPC 57/21, annex 4, paragraph 5.3). Section 6 of Procedure (G9) presents the 

evaluation criteria the Organization should apply in the evaluation of the information provided in 

the application. 

3 The competent authority in Norway has verified the application dossier and the test 

protocols applied for all tests undertaken and believes it to satisfy the data requirements 

of Procedure (G9) adopted by resolution MEPC.169(57). 
MEPC 60/2/8 - 2 - 

I:\MEPC\60\2-8.doc 

4 Norway therefore submits the non-confidential part of the manufacturer’s application 

dossier, in the annex of this document, to the Organization for evaluation according 

to Procedur (G9). The complete dossier will be made available to the experts of the 

GESAMP-BWWG with the understanding of confidential treatment. 

Action requested of the Committee 

5 The Committee is invited to consider the proposal for approval and decide as appropriate. 

*** 
MEPC 60/2/8 

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ANNEX 

NON-CONFIDENTIAL INFORMATION OF THE OCEANGUARDTM 

BALLAST WATER MANAGEMENT SYSTEM 

Contents 

1 ABBREVIATION 

 

2 SUMMARY 

3 SYSTEM DESCRIPTION 

3.1 Introduction of OceanGuardTM BWMS 

3.1.1 Automatic back flushing filter 

3.1.2 EUT unit 

3.1.3 Control unit 

3.1.4 Sensors 

3.2 Chemical reactions in the EUT unit 

3.2.1 Reactions in fresh water 

3.2.2 Reactions in seawater 

3.2.3 Secondary with the possibility of bromide ion in water 

3.2.4 Secondary reactions with the possibility of organics in water 

3.3 Treatment process 

3.4 Test results of biological efficacy 

4 IDENTIFICATION OF THE SUBSTANCES OR PREPARATIONS 

4.1 Preparations 

4.2 Active Substances 

4.2.2 Hydroxyl free radical 

4.2.3 Hydrogen peroxide 

4.2.4 Hypochlorite and hypochlorous acid 

4.3 Relevant Chemicals 

4.4 Others 

5 DATA OF ACTIVE SUBSTANCES GENERATED IN BALLAST WATER 

5.1 Hydroxyl free radical 

5.2 Hydrogen peroxide 

5.2.1 Physical and chemical properties of hydrogen peroxide 

5.2.2 Effects on aquatic organisms 

5.2.3 Toxic effects on mammals 

5.2.4 Environmental fate and effect under aerobic and anaerobic conditions 

5.2.5 Risk characterization 

5.3 Hypochlorous acid 

5.3.1 Physical and chemical properties of hypochlorous acid 
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5.4 Sodium hypochlorite 

5.4.1 Physical and chemical properties of sodium hypochlorite 

5.4.2 Effects on aquatic organisms 

5.4.3 Toxic effect on mammals 

5.4.4 Environmental fate and effect under aerobic and anaerobic conditions 

5.4.5 Testing methods 

5.4.6 Risk characterization 

5.4.7 PNEC/PEC evaluation 

6 DATA OF THE RELEVANT CHEMICALS IN BALLAST WATER 

6.1 Dibromochloromethane 

6.1.1 Physical and chemical properties of dibromochloromethane 

6.1.2 Effects on aquatic organisms 

6.1.3 Toxic effect on mammals 

6.1.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.1.5 Testing method 

6.1.6 Risk characterization 

6.1.7 PNEC/PEC evaluation (MAM-PEC) 

6.2 Tribromomethane 

6.2.1 Physical and chemical properties of tribromomethane 

6.2.2 Effects on aquatic organisms 

6.2.3 Toxic effect on mammals 

6.2.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.2.5 Testing methods 

6.2.6 Risk characterization 

6.2.7 PEC/PNEC evaluation 

6.3 Dibromoacetic acid 

6.3.1 Physical and chemical properties of dibromoacetic acid (DBAA) 

6.3.2 Effects on aquatic organisms 

6.3.3 Toxic effect on mammals 

6.3.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.3.5 Testing methods 

6.3.6 Risk characterization 

6.3.7 PNEC/PEC evaluation 

6.4 2,4,6-tribromophenol 

6.4.1 Physical and chemical properties of 2,4,6-tribromophenol 

6.4.2 Effects on aquatic organisms 

6.4.3 Toxic effect on mammals 

6.4.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.4.5 Testing methods 

6.4.6 Risk characterization 

6.4.7 PNEC/PEC evaluation 
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6.5 Bromate ion 

6.5.1 Physical and chemical properties of potassium bromate 

6.5.2 Effects on aquatic organisms 

6.5.3 Toxic effect on mammals 

6.5.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.5.5 Testing methods 

6.5.6 Risk characterization 

6.5.7 PNEC/PEC evaluation 

6.6 Carbon monoxide 

6.6.1 Physical and chemical properties of carbon monoxide 

6.6.2 Effects on aquatic organisms 

6.6.3 Toxic effect on mammals 

6.6.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.6.5 Analytical method 

6.6.6 Risk characterization 

6.7 Methane 

6.7.1 Physical and chemical properties of methane 

6.7.2 Effects on aquatic organisms 

6.7.3 Toxic effect on mammals 

6.7.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.7.5 Analytical method 

6.7.6 Risk characterization 

7 TOXICITY ASSESSMENT OF THE TREATED BALLAST WATER 

7.1 Contents of Oxidants 

7.2 Determination of holding time 

7.3 Ecotoxicity 

8 RISK ASSESSMENT 

8.1 Risks to the safety of the ship 

8.1.1 Corrosion 

8.1.2 Fire and exposure 

8.1.3 Storage, loading/unloading and noise 

8.2 Risks to human health 

8.2.1 Human exposure scenario (HES) 

8.2.2 Risk control measures 

8.3 Effects on the aquatic environment 

REFERENCES 
MEPC 60/2/8 

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1 ABBREVIATION 

μg/L Microgram per litre 

ATSDR Agency for Toxic Substances and Diseases Registry 

BCAA Bromochloroacetic Acid 

CAS Chemical Abstracts Service 

DBAA Dibromoacetic Acid 

DBPs Disinfection By-products 

EC50 Half Effective Concentration 

EPI Suite Environmental Estimation Program Interface Suite 

ESIS European chemical Substances Information System 

FC Free Chlorine 

EUT Electrocatalysis enhanced by Ultrasonic Technology 

HAAs Haloaceticacids 

IARC International Agency for Research on Cancer 

ICSC International Chemical Safety Card 

IMO International Maritime Organization 

ISO International Standardization Organization 

IUPAC International Union of Pure and Applied Chemistry 

Koc Sediments-water partition coefficient 

LC50 Half Lethal Concentration 

LD50 Half Lethal Dose 

LOAEL Lowest Observed Adverse Effect Level 

Log Pow Logarithm of octanol/water partition coefficients 

m3/d Cubic meter per day 

MBAA Monobromoacetic Acid 

MEPC Maritime Environment Protection Committee 

mg/kg/d Milligram medicines per kilogram weight per day 

mg/L Milligram per litre 

Ml Millilitre 

MOS Margin of Safety 

MOS(ref) Margin of Safety (reference) 

MSDS Material Safety Data Sheet 

NOAEL No Observed Adverse Effect Level 

NOEC No Observed Effect Concentration 

NTP National Toxicology Program 

PEC Predicted Effect Concentration 

PNEC Predicted No Effect Concentration 

Ppm Part per million (volume or mass ratio) 

THM Trihalomethanes 

TC Total Chlorine 

US EPA U.S. Environmental Protection Agency 

WHO World Health Organization 
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2 SUMMARY 

OceanGuardTM Ballast Water Management System (BWMS) is the technology 

of Qingdao Headway Technology Co., Ltd., which has been under development for five years. 

The technology uses advanced Electrocatalysis enhanced by Ultrasonic Treatment (EUT) to 

achieve the ballast water treatment. The ballast water goes through a 50 μm filter and the EUT 

unit during ballasting. At de-ballasting, the 50μm filter is bypassed and the water goes through 

the ultrasonic treatment and is discharged without applying the electrocatalysis. 

Small-scale testing of the ballast water treatment technology has been carried out by NIVA at 

their test facilities in Norway in January 2009. NIVA has established a centre for land-based, 

full-scale testing of ballast water management systems in accordance with IMO Guidelines and 

has operated laboratories which are accredited according to the international standards, 

i.e. “NS-EN ISO/IEC 17025”. The whole testing was under the supervision of DNV. 

The small-scale tests performed at NIVA have been carried out using the medium salinity water 

(between 3 and 32 PSU, approximately. 22 PSU) and high salinity water (>32 PSU) according 

to Guidelines (G8). For both water qualities, 1, 2 and 4 mg/L were set as the 

initial Total Residual Oxidants (TRO) level in the EUT. The test results show that the ballast 

water can reach the D-2 standard after treatment. Active Substances and other chemicals have 

been identified, and the concentrations of the Relevant Chemicals are found to be in direct 

proportion to the TRO concentration generated during ballasting. Considering the decay rate of 

TRO, the concentration of Relevant Chemicals generated, and the toxicity testing results, initial 

TRO concentrations of 1 mg/L and 2 mg/L have been found to be sufficient for treatment of 

seawater (33 PSU) and brackish water (22 PSU) respectively. In this application, all testing 

results arrive from the small-scale tests performed at NIVA. Additional test results are indicated 

in the attached NIVA report. 

In the testing cycle with seawater (33 PSU) treated with the initial TRO level of 1 mg/L, 

after 1 day storage, the TRO level was below 0.2 mg/L. On day 5, i.e. after 5 days storage, only 

very few chemical substances in low concentration were detected, and no explosive or toxic gas 

was detected. According to the related OECD or ISO standard (NIVA report), undiluted treated 

water has some toxicity to aquatic organisms, however, after low dilution, it will be suitable to 

discharge into the environment nearby. 

In the test with brackish water (22 PSU) with the initial TRO level of 2 mg/L, after 1 day storage, 

the TRO level was below 0.2 mg/L, however, carbon monoxide and methane in low 

concentration was detected during ballasting. On day 5, only a few chemical substances in low 

concentration were detected, and no carbon monoxide, or methane, or other explosive or toxic 

gas was detected. According to related toxicity testing results, even undiluted treated water did 

not show significant effect to aquatic organisms. 
MEPC 60/2/8 

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The biological efficacy is achieved mainly through Active Substances generated in the water, 

which we call TRO. The ultrasonic part acts as a supplementary of the electrocatalysis part, to 

enhance the biological efficacy. In seawater and brackish water, which contain chloride ion, TRO 

are mainly in the form of sodium hypochlorite. In fresh water, since the concentration of chloride 

ion is low, TRO in the water are mainly in the mode of oxidants with high oxidizing ability, 

composing of the elements hydrogen and oxygen, and some sodium hypochlorite. Theoretically, 

the degradation rate of TRO in fresh water is much faster than that in seawater, and the 

concentration of chemical substances generated is even lower, so there is basically no harmful 

effect to the environment. Toxicity of the treated waters with low salinity should be smaller than 

that of water with high salinity. Toxicity of water of different salinities treated with the same 

initial TRO level, should be in direct proportion to the salinity. 

The mechanical filter to be used has a filter mesh of 50 μm. The filter can remove particles and 

viable organisms ≥ 50 μm in minimum diameter. After a certain time of storage, since there will 

be re-growth of bacteria and other organisms in order to make sure water being discharged can 

still reach requirements of regulation D-2, a second treatment by the EUT unit will be conducted 

during de-ballasting before discharge over a long period of travel. Only the ultrasonic part works 

during this process. 

In this application for Basic Approval, only small-scale testing has been carried out. During 

application for Final Approval, equipment tested will be completely the same as the final 

product, including treatment unit, automatic control unit, etc., as required by IMO. The treatment 

unit adopted the design of modular structure, with 250t/h flow for each module, which makes the 

system suitable to be installed on ships with different ballast water capacities. 

The ballast water treatment is performed in a totally sealed system and all Active Substances are 

generated in the EUT unit. This makes it unnecessary to buy or store any additional chemicals 

on board and eliminates the hazards related to storage and handing of extra chemicals. 

Results from toxicity testing of the treated ballast water are in line with what was expected from 

the PEC/PNEC assessment of Active Substances. Available data therefore do not indicate that 

there are Active Substances produced by the Ocean GuardTM which are not already accounted for 

in the present assessment. 

Active Substances were also assessed for their Persistence, Bioaccumulation and Toxicity (PBT) 

potential. Although sodium hypochlorite shows significant chronic toxicity and tribromomethane 

is fairly persistent in the environment, no Active Substance fulfilled more than one of 

the PBT criteria, and none therefore are eligible for a PBT classification. 
MEPC 60/2/8 

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3 SYSTEM DESCRIPTION 

3.1 Introduction of OceanGuardTM BWMS 

Sea Door P

Symbols

Valve

Filter

P Ballast Pump

Control 

Water Tank

Electromagnetic 

Flow sensor EM

EUT 

Power Electrically Operated Valve

PSU

Outlet

Sewage 

Outlet

EM

Treated Water 

Tank

PSU Salinity Sensor

EUT 

Unit Sample 1

Sample 2

Sample 3

Sample 4

Figure 3.1 : Treatment Process with OceanGuardTM Ballast Water Management System 

Figure 3.2 : Model of OceanGuardTM Ballast Water Management System 
MEPC 60/2/8 

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Figure 3.1 shows an OceanGuardTM BWMS with one single treatment unit of 250 t/h. Ballast 

water is pumped in from the sea chest, through the filter and into the EUT unit. After the 

ultrasonic treatment and electrocatalysis in the EUT unit, which kills the aquatic organisms, the 

water flows through the ballast water pipes into the ballast water tanks. During de-ballasting, the 

ballast water bypassed the filter and pumped into the EUT unit where only the ultrasonic unit is 

used before discharge. Figure 3.2 shows the model of the OceanGuardTM Ballast Water 

Management System. 

The key components of OceanGuardTM Ballast Water Management System are described in the 

following paragraphs. 

3.1.1 Automatic back flushing filter 

In order to prevent particles and viable organisms ≥50 μm in diameter from getting into the 

system, an automatic back-flushing filter with the filtration degree of 50μm is set before the 

treatment unit. This filter will start backwashing automatically when the pressure loss exceeds 

the set point without any artificial operations. The filter is working during ballasting, while 

during de-ballasting, it is bypassed. 

Figure 3.3 : Automatic back flushing filter 

3.1.2 EUT unit 

This part is the core component of the system. It is composed of two parts: the electrocatalysis 

part and the ultrasonic part. In the electrocatalysis part, semiconductor catalyzing materials of 

high performance are adopted, which generate the Active Substances. The electrocatalysis part 

can realize high current efficiency, with long lifespan of more than two years, suppose working 

hours is 24-hour per day. It can remove the vast majority of the remaining biological bacteria. 

The ultrasonic part adopts the technology now commonly used in sterilization technology. It can 

generate oscillating force within very short period of time, crush cells, so the bactericidal effect 

can be realized. As a supplementary part of the electrocatalysis unit, this can further improve the 

sterilization effects. 
MEPC 60/2/8 

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Figure 3.4 : EUT unit 

3.1.3 Control unit 

The control unit for the entire system is in charge of various types of sensors, handling of alarm 

signals, as well as startup and shutdown of the system. It contains all the necessary controlling 

procedures and displays the operating conditions of every components of the system. If the 

treatment system fails, it will make an audio and light alarm and automatically switch to a safe 

mode. Data of operating conditions of the system can be recorded, memorized, displayed and 

printed. The operators can take control and make adjustment through this control unit. 

3.1.4 Sensors 

Parameters like salinity, flow rate, TRO and EUT power consumption can be measured by the 

sensors. The control unit can respond on the system condition and initiate adjustments accurately 

in time to get an ideal treatment effect. Salinity, flow rate and TRO are very important 

parameters in the process. The most suitable initial operational mode of the EUT unit can be set 

by the control unit through the internal memory procedures. With the TRO sensors, power 

supply parameters can be adjusted by the control unit, so that suitable initial TRO level can be set 

to ensure the biological treatment efficacy and also to limit the toxicity. Figure 3.5 shows the 

principle of the control system. 

Data from TRO sensors will be transmitted to the control unit. If the data is higher than the 

required value set, parameters of EUT power supply will be adjusted to lower the initial TRO 

level, and vice versa. Therefore, the initial concentration of TRO will remain in a range of 

constant concentration. 
MEPC 60/2/8 

ANNEX 

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Figure 3.5 : Principle of the control system 

The laboratory testing system mainly includes the automatic back-flushing filter and EUT unit. 

3.2 Chemical reactions in the EUT unit 

The EUT unit can remove and kill the organisms by combing the technologies of electrocatalysis 

and ultrasonic sound. The chemical reactions take place in the electrocatalysis part of the EUT 

unit. The electrocatalysis unit kills the organisms mainly by using the online-generated hydroxyl 

free radical, which has extremely strong oxidizability to oxidize the cell wall and cause the 

damage and death of the organisms. Meanwhile, on the surface of the semiconductor catalyst, it 

can make a direct oxidation of the organisms. 

Some semiconductor catalyst material may cause cavitation effect in the electric field. 

The cavitation has very high ability to capture electrons, so that the redox reactions on the 

surface of the materials and in the solution were triggered. In the redox reactions of the solution, 

H2O become ·OH by losing electrons, which is of high oxidation ability. This free radical will 

either take decomposition reaction or go on reacting with the other ions and molecules in the 

water and then generate other kinds of oxidizing substances like hydrogen peroxide. Because of 

their strong oxidizability, these substances will continue taking reactions with organisms and 

other substances in the water and change into other products. All of these oxidizing substances 

have the effective components of oxidizing the organisms. In this application, the oxidizing 

substances are narrated as TRO. 
MEPC 60/2/8 

ANNEX 

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3.2.1 Reactions in fresh water 

At the Anode OH Cat ⋅ OH − Cat + e − (a) 

⋅OH − Cat === O − Cat + H + e + (b) 

2⋅OH −Cat === O −Cat + H2O (c) 

2 O Cat O Cat ⋅ − === 2 + (d) 

2·OH-Cat===H2O2+Cat (e) 

2H2O2====2H2O+O2 (f) 

At the Cathode (g) 2H + 2e === H2

+ (g) 

As the oxidation potential of hydroxyl is much higher than that of chlorine, the generated 

hydroxyl will oxidize chloride immediately into chlorine, hypochlorite or hypochlorous, 

depending on different pH values of the water. See figure 4.1. 

3.2.2 Reactions in seawater 

At the Anode OH Cat ⋅OH −Cat + e − (a) 

⋅ OH − Cat === O − Cat + H + e + (b) 

2⋅OH −Cat === O −Cat + H2O (c) 

2 O Cat O Cat ⋅ − === 2 + (d) 

2·OH-Cat===H2O2+Cat (e) 

2H2O2====2H2O+O2 (f) 

Cl Cat ⋅Cl −Cat + e − (g) 

Cl Cat Cl2 2⋅ − === (h) 

Reactions in the water − + Cl + H O === ClO + Cl + 2H -

2 2 (i) 

At the Cathode (g) 2H + 2e === H2

+ (j) 

3.2.3 Secondary reactions with the possibility of bromide ion in water 

If there is a fraction of bromide in the seawater, the bromide ion can be oxidized into 

hypobromous acid or hypobromite by hypochlorite or hypochlorous. These substances will take 

reactions with the organics in the water and produce DBPs. 

− Br + HOCl === HOBr + Cl - (k) − + HOBr (l) === OBr + H
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3.2.4 Secondary reactions with the possibility of organics in water 

The formation and main components of DBPs are under the influence of many factors, such as 

the water quality, including TOC, bromide ion concentration, pH value and temperature. DBPs 

can also be affected by the treatment conditions like dose, and the removal extent of the organics 

before treatment, etc. All the chemical substances that maybe generated during the process have 

been tested (NIVA report). See test results in figures 4.1 and 4.2. 

Reactions: HOBr+Organics===CHBr3

3.3 Treatment process 

Figure 3.6 : Experiment layout 

Simulative ballast tanks for treated and control ballast water were set up according to the IMO 

requirements. Tanks for treated water and control water are sealed. Tests with seawater (33 PSU) 

and brackish water (22 PSU) were carried out in different time period, with the same procedure 

and a flow rate of 2 m3

/h. 

Ballasting of treated water and control water was on the same day. Test water was pumped in, 

through the filter and the EUT unit, into the 1 m3 treated water tank. On day 5, pump was adopted 

to mix the water in the tank. Treated water was discharged without second treatment of the EUT 

unit. Samples were collected from the pipe. 

For control water, test water was pumped in, and directly came into the 1 m3 control water tank. 

On day 5, pump was adopted to mix the water in the tank. Control water was discharged through 

the pump directly and samples were collected then. All tanks were closed with a lid and covered 

to protect from light (refer to section 2.4.1, NIVA report). 
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3.4 Test results of biological efficacy 

Environmental settings and conditions of sampling are set according to the IMO requirements in 

the four tests with different water qualities and salinities. Guidelines (G8) requirements for test 

water have been fulfilled in all the tests. During the whole process, the system shows good 

stability and effectiveness, with the flow rate of 2 t/h. See testing results in Table 3.1(refer to 

pages 30 to 33, NIVA report). 

Table 3.1 : Test results of biological efficacy 

Detection Control water Treated water 

Item 

Salinity

(PSU) 

TRO 

(mg/L) Day 0 Day 5 Day 0 Day 5 

Requirement 103/ml >100/ml <10/ml 

33 1 9248 7779 0.7 0.3 0-50μm Organisms 22 2 3008 2852 0 0 

Requirement 104(cfu/ml 

33 1 7.9x104 9.2x104 1.3x103 4.5x103

Heterotroph 22 2 1.3 x 105 1.5 x 10 2.8 x 10 3.0 ± 0.3 x 105

Requirement E.coli<250 cfu/100ml 

33 1 1.6x100 0 0 0 0 Coliform group 22 2 1 0 0 0 0 

Requirement V. cholerae <1cfu/100ml

33 1 1.7x103 1.9x103 1.3x101 1.8x100 < 1 Vibrio group 22 2 2.2 x 103 3.2 x 10 1.3 x 10 1.6 x 10 < 1 

Requirement Int.Ent.<100 cfu/100ml 

33 1 0 0 0 0 0 

Enterococci 22 2 0 0 0 0 0 

4 IDENTIFICATION OF THE SUBSTANCES OR PREPARATIONS 

4.1 Preparations 

In the OceanGuardTM System, the only component that generates chemical substances is the EUT 

unit, in which a certain concentration of free radical group like hydroxyl free radical will be 

generated on the activator’s surface. Chloride and other ions or organics will be oxidized by this 

free radical, then hypochlorous or other kinds of substances will be generated. During the whole 

process, no chemicals are needed, so there is no need to buy, store, or transfer chemicals on board. 

4.2 Active Substances 

4.2.1 Total Residual Oxidants (TRO) 

There are some chemical reactions in the EUT unit (refer to section 3.2), and some Active 

Substances are generated, which we call TRO. TRO do not refer to one specific substance; it is 

the generic term for a class of substances with oxidizability. Many substances can not be 

measured because of their instability, so TRO in this application refer to all the oxidants which 

have the ability of disinfection. DPD method is used during the tests to measure the 

concentration of Total Chlorine (TC) and Free Chlorine (FC), with the unit of mg/L chlorine. 

Substances with oxidizability react with the DPD preparation, and stable compound with red 

colour will be generated. 

Active Substances generated in the EUT unit include hydroxide radical, hypochlorous acid, 

hypochlorite and hydrogen peroxide. 
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4.2.2 Hydroxyl free radical 

Active Substances generated directly on board are hydroxyl free radicals, or there might be 

hydrogen peroxide, oxygen free radical in low concentration, which can be indicated from the 

chemical reactions. The substances have very high oxidation potential with the extremely short 

generation and existence time of nanosecond. Since the existence time is so short, it is almost 

impossible to carry out the concentration measurement. 

George V. et al. have listed the varied reaction kinetics parameters in every kind of solution. 

They had worked over the rate constant of some kinds of unstable substances in different 

solutions. Many documents show that the oxidizability of hydroxyl free radical second only to 

fluorine, so hydroxyl free radical can take various reactions with almost all biomacromolecules, 

organics and inorganics. Hydroxyl free radical can have direct or indirect redox reactions with 

most of the micro-organisms and organics in water. The reactions hydroxyl free radical takes are 

the free radical reaction, which is very fast, and while reacting with organics the rate constant is 

always above 109 L/ (mol ·s), which reaches or goes beyond the limiting value of diffusion rate 

[ 1010 L/ (mol ·s) ]. Thus, it is difficult to measure its accurate concentration by instruments for 

the very short existence time of hydroxyl free radical. 

4.2.3 Hydrogen peroxide 

Hydrogen peroxide is a kind of common used disinfectant, which has very strong oxidability and 

short lifespan. Theoretically, hydrogen peroxide can react with hydroxide radicals in the EUT 

unit. However, no evidence was detected in the pilot testing. Description about this substance is 

in section 5 of this application. 

4.2.4 Hypochlorite and hypochlorous acid 

According to the formula (g)-(h) of reactions in seawater, the mixture consists of one or several 

substances of chlorine, hypochlorous acid and hypochlorite generated from reactions between 

hydroxyl free radical and sodium chloride. The percentage concentration of chlorine, hypochlorous 

acid and hypochlorite in the mixture will vary with different pH values (see figure 4.1). 

When pH<5, there will be chlorine and hypochlorous acid. When the pH value is between 5 

and 10, there will be hypochlorite and hypochlorous acid. When pH>10, there will be 

hypochlorite. Since the pH value of ballast water is between 7 and 8, they will be mainly in the 

form of hypochlorite and hypochlorous acid, and there is no outlier chlorine detected from the 

testing results. Hypochlorous acid and hypochlorite are both listed here as the Active Substances. 
MEPC 60/2/8 

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4.3 Relevant Chemicals 

DBPs are generated by the reactions of Active Substances, organics and bromide ion in the water, 

including THMs, HAAs and so on. These substances are paid close attention to in recent years as 

they may cause carcinogenicity and organism accumulations. Also this kind of substances may be 

a threat to human health with their steady chemical property and long half-life, as they may 

accumulate in the organisms, so the generating quantity must be reduced. During the tests, 

substance tested includes AOX, EOX, bromate ion, THMs, phenol and other halogenation 

organics. As it is shown in Table 4.1, tribromomethane is the main THMs in the tested 

halogenation organics listed. In the tests selected, i.e. seawater (33 PSU), treated with 1 mg/L 

initial TRO, and brackish water (22 PSU), treated with 2 mg/L initial TRO, the maximum levels 

detected are as follows: DBCM 1.7 μg/l, tribromomethane150 μg/l, DBAA 5.9 μg/l, 2.4.6-

tribromophenol 0.1 μg/l and bromate ion 3.5 μg/l (refer to section 3.5, NIVA report). Therefore, 

the five substances above-mentioned are identified as Relevant Chemicals (Table 4.2). 

Table 4.1 : DBPs concentration in seawater (33 PSU) and brackish water (22 PSU) tests 

(samples are collected after 5-day storage). 

Component Unit Seawater (33 PSU) 

Day 5 

Brackish water 

(22 PSU) 

Day 5 

Chloroform μg/l <0.50 <0.50 

Bromodichloromethane μg/l <0.50 <0.50 

Dibromochloromethane μg/l 1.7 5 

Tribromomethane μg/l 44 150 

Monochloroacetic acid μg/l <0.50 <0.50 

Dichloroacetic acid μg/l <0.30 <0.30 

Acetocaustin μg/l <0.20 <0.20 

Bromoacrtic μg/l <0.20 <0.20 

Dibromoacetic acid μg/l 0.66 5.9 

Bromochloroacetic acid μg/l <0.10 <0.10 

Bromodichloroacetic acid μg/l <0.10 <0.10 

Chlorodibromoacetic acid μg/l <0.10 <0.10 

Tribromoacetic acid μg/l <0.10 <0.10 

2,4-Bromophenesic acid μg/l <0.10 <0.10 

2,6-Bromophenesic acid μg/l <0.10 <0.10 

2,4,6-Bromophenisic acid μg/l <0.10 0.1 

1,2- Nephis μg/l <1.0 <1.0 

1,2,3- Trichloropropane μg/l <1.0 <1.0 

2- Chlorotoluene μg/l <0.50 <0.50 

4- Chlorotoluene μg/l <0.50 <0.50 

1,2-dibromo-3- 

Chloropropane μg/l <1.0 <1.0 

1,2,3- Tribromo-benzene μg/l Note note 

1,3,5- Tribromophenol μg/l <1.0 <1.0 

AOX mg/L 0.02 0.1 

EOX mg/L <0.010 0.012 

Bromate ion μgl 1.0 3.5 
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Table 4.2 : Detected Relevant Chemicals in treated ballast water (the highest concentration 

in the tested waters of different quality) 

Name Concentration (μg/L) 

Dibromochloromethane 1.7 

Tribromomethane 150 

Dibromoacetic Acid 5.9 

Tribromophenol 0.1 

Bromate Ion 3.5 

4.4 Others 

According to the reaction formulas in section 3.2, a certain amount of hydrogen and chlorine will 

be generated at the cathode of the EUT unit, and most hydrogen will escape on the surface 

because of its low water solubility. Hydrogen will violently react with oxygen and cause 

explosion once the explosion limit of 4% is reached. So, concentrations of hydrogen and oxygen 

are also measured besides chlorine. While the system is operating, chlorine may be generated in 

the high TRO concentration condition. Chlorine is a toxic gas with high hazard to human body. 

Carbon monoxide, methane and hydrogen sulfide are the products from the incomplete oxidation 

of TRO and the organics in a high concentration of the organics in the water. Also, carbon 

monoxide is toxic gas. The United States Occupational Safety and Health Administration 

(OSHA) had specified the concentration threshold for long-term contact in workshop as 50 ppm. 

Methane is a flammable gas and it will cause explosion once the concentration reaches 5%-15% 

in air. Hydrogen sulfide is also flammable, and makes adverse effects on human body 

(human LC50 is 500 ppm). So these kinds of gases are harmful to human and ship. 

Table 4.3 : Concentration of gas detected (Refer to section 2.3, NIVA report) 

 Unit Salinity (PSU) TRO (mg/L) Day 0 Day 5 

Hydrogen % LEL 33 1 0 0 

22 2 0 0 

Chorine ppm 33 1 0 0 

22 2 0 0 

Oxygen % 33 1 20.9 20.9 

22 2 20.9 20.9 

Carbon 33 1 0 0 

monoxide 

ppm 

22 2 25 0 

Hydrogen 33 1 0 0 

sulfide 

ppm 

22 2 0 0 

Methane % LEL 33 1 0 0 

22 2 2.5 0 
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Listed above are the results from the selected testing cycles. In test with seawater of 33 PSU, 

treated by 1 mg/L initial TRO, concentration of oxygen is in normal, no other testing gases are 

detected. In test with brackish water of 33 PSU, treated by 2 mg/L initial TRO, 25 ppm carbon 

monoxide and 2.5% methane are detected (Refer to section 2.3, NIVA report). The 

above-mentioned 25 ppm carbon monoxide, 2.5% methane is analysed in the HES assessment. 

5 DATA OF ACTIVE SUBSTANCES GENERATED IN BALLAST WATER 

5.1 Hydroxyl free radical 

Due to the momentary life of hydroxyl free radical, it will react with the organics and inorganics 

completely by the moment it is generated, and these reactions will produce a series of other 

oxidative substances in the form of TRO. Since the lifespan of hydroxyl free radicals is very 

short, it can only exist in the EUT unit. For this free radical itself, it is hard to take concentration 

measurement, and it will not cause any effects for relative staff or the environment. Meanwhile, 

existing research about hydroxyl free radical is very few, so we can not provide more data in 

detail. Only the following data can be provided. 

CAS No. 3352-57-6 

Name Hydroxyl radical 

Formula · OH 

Molecular weight (g/mol) 17.01 

Structural formula HO 

Redox potential 2.8 V 

5.2 Hydrogen peroxide 

5.2.1 Physical and chemical properties of hydrogen peroxide 

Property Value References 

CAS No. 7722-84-1 

Molecular formula H2O2

Molecular Weight (g/mol) 34.02 

Structural formula HO-OH 

Melting point (°C) -0.43 OSHA, H2O2

Boiling point (°C) 152 OSHA, H2O2

Flammability Not combustile 

Density (20°C, water=1) 1.39 ATSDR, H2O2

Vapour pressure (30°C, 

mmHg) 

5 OSHA, H2O2

Vapour density (air=1) 1.2 ATSDR, H2O2

Solubility in water (0°C) Soluble OSHA, H2O2

PH in solution Weak acid; PH values change according 

to concentration 

HSDB, H2O2

Dissociation constant (pKa, 

25°C) 

11.75 HSDB. H2O2
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Oxidation/ reduction 

potential 

1.8 MEPC 55/2/4, annex

page 6 

Corrosion to material or 

equipment 

It can react with some materials. 

Reactivity to container 

material 

Contact with metals could result in 

explosions. 

OSHA, H2O2

Auto-ignition temperature N/A 

Explosivity Contract with combustile materials may 

cause ignition or combustion. Mixed with 

some special organic materials can cause 

explosions. 

OSHA, H2O2

Oxidizability Powerful oxidizer 

Surface tension (20°C) 80.4 dynes/cm HSDB, H2O2

Viscosity 1.245 centipoises(liquid) HSDB, H2O2

Thermal stability and 

decomposition product 

Exposure to heat can create potential fire 

or explosion hazard 

OSHA, H2O2

Octanol- water partition 

coefficients (log Pow) 

-1.57 EPI Suite v3.2 

Sediment- water partition 

coefficients (Koc) 

14.3 EPI Suite v3.2 

Henry 

constant (Pa.m3

/mole, 

20°C) 

7.5E-4 EU risk assessment 

EPI Suite is downloaded from the EPA website. In situation where documents are 

incomplete, this software is used to make an analysis of the Relevant Chemicals. 

The Estimation Programs Interface (EPI) SuiteTM is a Windows®-based suite of 

physical/chemical property and environmental fate estimation program developed by the EPA’s 

Office of Pollution Prevention Toxics and Syracuse Research Corporation (SRC). EPI SuiteTM 

uses a single input to run the following estimation programs: KOWWINTM, AOPWINTM, 

HENRYWINTM, MPBPWINTM, BIOWINTM, BioHCwin, KOCWINTM, WSKOWWINTM, 

WATERNTTM, BCFBAFTM, HYDROWINTM, KOAWIN and AEROWINTM, and the fate models 

WVOLWINTM, STPWINTM and LEV3EPITM. ECOSARTM, which estimates ecotoxicity, is also 

included in EPI SuiteTM.EPI SuiteTM is a screening-level tool and should not be used if acceptable 

measured values are available. 
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5.2.2 Effects on aquatic organisms 

5.2.2.1 Acute aquatic toxicity 

 Species Effect Value(mg/L) References 

Bluegill (fresh) 96hLC50 26.7 ECOTOX database 

Cutthroat trout (fresh) 30minLC50 514 ECOTOX database 

Rainbow trout (fresh) 96hLC50 22 ECOTOX database 

Dusky spinefoot (sea) 24hLC50 224 ECOTOX database 

Jack Mackerel (sea) 24LC50 89 ECOTOX database 

Fish 

Chameleon goby (sea) 24LC50 155 ECOTOX database 

Water flea (fresh) 24hEC50 2.3 ECOTOX database Crustacea Water flea (fresh) 48hEC50 24 ECOTOX database 

Blue green algae (fresh) 90minEC50 3.4 ECOTOX database Algae Blue green algae (fresh) 22hminEC50 0.9 ECOTOX database 

5.2.2.2 Chronic aquatic toxicity 

 Species Effect Value(mg/L) Reference 

Mollusca Zebra mussels 

(fresh) 56dNOEC 2 EU risk assessment 

5.2.2.3 Information on endocrine discrupiton 

There is no relevant data available. 

5.2.2.4 Sediment toxicity 

Koc of hydrogen peroxide is 14.3 L/kg (EPI SuitTM, v3.20), which is lower than the limit value 

Koc of 500 L/kg . Thus, the substance is not likely to accumulate in sediments and testing with 

sediment dwelling species is not relevant for the assessment. 

5.2.2.5 Bioconcentration/biomagnification 

Log Pow of hydrogen peroxide is -1.57 (EPI SuitTM, v3.20), which is lower than the limited Log 

Pow of 3, indicating a very low potential for bioconcentration/biomagnification. 

5.2.2.6 Food web/population effects 

Log Pow of hydrogen peroxide is -1.57 (EPI SuitTM, v3.20), which is lower than Log Pow 3 that 

is limit value. So the possibility of hydrogen peroxide’s impact to food web and population effect 

should be insignificant. 
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5.2.3 Toxic effects on mammals 

5.2.3.1 Acute toxic effect on mammals 

Species Effect Value(g/kg) Reference 

Male and female rats Oral LD50 0.8-5 EU risk assessment 

Rabbits Dermal LD50 9.2 EU risk assessment 

Mice and rats Inhalation LD50 2 g/m3 EU risk assessment 

Part of the data in this article can not be written more clearly, because it is not described in detail 

in the reference. Descriptions are made in as much detail as possible based on the references. 

5.2.3.2 Effects on skin and eye 

 Species Method Results Reference 

Skin Rabbits 3%-8%, single Mild reactions EU risk assessment 

Rabbits 22 ppm, daily for 3 

months 

Eye No eye injury HSDB,H2O2

Rabbits 0.5% solution, single Disturbance of epithelium 

and returned to normal 

within 24 h. 

HSDB,H2O2

5.2.3.3 Repeated-dose toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

Dose 

Species Results Reference 

Oral 90 days 100-

3,000 

ppm 

solution 

Mice Body weights reduced; food 

and water consumption. 

NOAEL=100 ppm 

EU risk 

assessment 

Dermal 4 months, 

5 h/day, 

5 days/week 

0.1-10.1 

mg/m3

Rats Threshold concentration 

was 1 mg/m3, no-effect 

concentration was 0.1 

mg/m3

EU risk 

assessment 

Inhalation 6 months, 

6 h/day, 

5 days/week 

10 

mg/m3

Dogs Skin irritation, sneezing. 

Skin thickened, hair 

bleached. 

HSDB,H2O2

5.2.3.4 Development and reproductive toxicity 

Pregnant rats were fed containing 10% hydrogen peroxide. Maternal and fetal weights were 

reduced but no significant malformation was reported (HSDB, H2O2). 
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5.2.3.5 Carcinogencity/mutagenicity/reproductive toxicity 

There is limited evidence in experimental animals for the carcinogenicity of hydrogen peroxide. 

Overall evaluation: Hydrogen peroxide is not classifiable as to its carcinogenicity to humans 

(Group 3) (HSDB, H2O2). 

Hydrogen peroxide was proven to be mutagenic to Salmonella typhimurium TA92 and TA102 

and was positive in a forward mutation test in Salmonella typhimurium SV50 (HSDB, H2O2). 

5.2.3.6 Toxicokinetics 

When hydrogen peroxide comes in contact with catalase, an enzyme found in blood and most 

tissues, it is rapidly decomposed into oxygen and water (HSDB, H2O2). 

5.2.3.7 Human toxicity 

Workers exposed to vapours from 90% H2O2 have noted irritation primarily, but splash of such 

high concentration is generally feared as potential cause of sever corneal damage. A 33-year old 

woman unintentionally ingested a 1 pint bottle of 35% hydrogen peroxide. She vomited, 

collapsed, and experienced a brief tonic-clonic seizure within minutes. The patient was markedly 

cyanotic and had copious white foam emanating from her mouth. After therapy, she was 

transferred to a rehabilitation facility (HSDB, H2O2). 

5.2.4 Environmental fate and effect under aerobic and anaerobic conditions 

5.2.4.1 Modes of degradation 

Environment Degradation 

outcome 

Period Results Reference 

Abiotic, seawater, 

sunlight 

Oxygen and 

water 

 Half-life(90% 

purity) was 8.3 

days 

EPA review of 

hydrogen peroxide 

Aerobic, water, 

non-sterile conditions 

oxygen and 

water 

 Half-life was 1.1-

5.3 h 

EPA review of 

hydrogen peroxide 

Aerobic, water, sterile 

conditions 

oxygen and 

water 

 Half-life was 80 h EPA review of 

hydrogen peroxide 

Anaerobic, soil Half-life was 4h EPA review of 

hydrogen peroxide 

5.2.4.2 Reactions with the organics 

Hydrogen peroxide may react as an oxidant, as a reductant or form addition compounds. It reacts 

easily with various functional groups. Most aromatic and aliphatic amines as well as most 

aldehydes do react with hydrogen peroxide (EU risk assessment). 

5.2.4.3 Potential physical effects on wildlife and benthic habitats 

No information is observed that hydrogen peroxide makes effects on wildlife or benthic habitats. 

Considering the extremely low (-1.57) and Koc (14.3) value, this effect can be ignored. 
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5.2.4.4 Potential residues in seafood 

Residues of hydrogen peroxide is almost impossible to be found in seafood, because it has no 

bioaccumulation and biomagnification toxicity. 

5.2.5 Risk characterization 

Criteria PBT Criteria Reach the Criteria or not 

Persistence Half life 

In seawater > 60 days, or in fresh water > 40 

days, or in seawater sediment >180 days, or in 

fresh water sediment >120 days. 

No (refer to section 5.2.4.1) 

Enrichment BCF > 2,000 or LogP ≥ 3 No (refer to section 5.2.1) 

Toxicity Chronic NOEC<0.01 mg/L No (refer to section 5.2.3.3) 

5.3 Hypochlorous acid 

Hypochlorous acid has even stronger oxidability than that of hypochlorite, and it has extremely 

short lifespan. It reacts with other substances immediately after being generated in the EUT unit. 

Since the properties of hypochlorous acid and hypochlorite are similar to each other, here only 

physical and chemical properties are listed below. For other data, please refer to section 5.4 on 

sodium hypochlorite in this application. 

Physical and chemical properties of hypochlorous acid 

Property Value References 

CAS No. 7790-92-3 

Molecular formula HOCl 

Molecular Weight (g/mol) 52.46 

Structural formula 

Melting point (°C) N/A 

Boiling point (°C) N/A 

Flammability Non-flammability 

Density (25°C) N/A 

Vapour pressure (20°C, Pa) N/A 

Vapour density (20°C, air=1) N/A 

Solubility in water (0°C) Soluble 

PH in solution N/A 

Dissociation constant (pKa, 25°C) 7.5 EHC, 216 

Oxidation/ reduction potential 1.49 EHC, 216 

Corrosion to material or equipment Corrosive to active metal material 

Reactivity to container material React with many material because 

of its oxidizability 

Auto-ignition temperature N/A 

Explosivity N/A 

Oxidizability Strong oxidizability 

Surface tension N/A 

Viscosity (20°C) N/A 

Thermal stability and 

decomposition product 

Generate chloric acid and chlorine 
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Octanol- water partition 

coefficients (log Pow) 

-0.87 EPI Suite 

v3.2 

Sediment- water partition 

coefficients (Koc) 

14.3 EPI Suite 

v3.2 

Henry constant (Pa.m3/mole) 1.277E-14 EPI Suite 

v3.2 

5.4 Sodium hypochlorite 

5.4.1 Physical and chemical properties of sodium hypochlorite 

Property Value References 

CAS No. 7681-52-9 

Molecular formula ClO·Na 

Molecular Weight (g/mol) 74.4 

Structural formula Na+ClO- 

Melting point (°C) -20─-30 ESIS, 2007 

Boiling point (°C) 96-120 ESIS, 2007 

Flammability Non-flammability ESIS, 2007 

Density (25°C) 1.23 g/cm3

 ESIS, 2007 

Vapour pressure (20°C, Pa) 17.4-20 hPa ESIS, 2007 

Vapour density (20°C, air =1) N/A 

Solubility in water (0°C) Soluble (29.3 g/100g water) ESIS, 2007 

PH in solution N/A 

Dissociation constant (pKa, 25°C) 7.5 EHC, 216 

Oxidation/ reduction potential 1.7 MEPC 56/2/3, 

annex, page 8 

Corrosion to material or 

equipment 

Corrosive to active metal 

material 

Reactivity to container material Can react with many material 

because of its oxidizability 

Auto-ignition temperature N/A 

Explosivity Anhydrous sodium 

hypochlorite is explosive 

ESIS, 2007 

Oxidizability Strong oxidizability, used and 

stored in water usually 

ESIS, 2007 

Surface tension N/A 

Viscosity (20°C) 2.6mPa.s MEPC 57/2/7, 

annex, page 17 

Thermal stability and 

decomposition product 

Generate sodium chlorate and 

sodium chloride 

ESIS, 2007 

Octanol- water partition 

coefficients (log Pow) 

-3.42 EPI Suite v3.2 

Sediment- water partition 

coefficients (Koc) 

14.3 EPI Suite v3.2 

Henry constant (Pa.m3/mole) 0.39 ESIS, 2007 
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5.4.2 Effects on aquatic organisms 

5.4.2.1 Acute aquatic toxicity 

 Species Effect Value 

(μg/L) References 

Clupea harengus (sea) 24hLC50 360 Dempsey, C.H., 1986 

Bluegill (fresh) 96hLC50 2130 Wilde, E.W., et al., 1983 

Silverside (sea) 96hLC50 143 Fisher, D.J., et al., 1999 

Golden shiner (fresh) 96hLC50 304 Fisher, D.J., et al., 1999 

Menidia beryllina (sea) 96hLC50 128 Fisher, D.J., et al., 1994 

Rainbow trout (fresh) 96hLC50 59 Fisher, D.J., et al., 1999 

Pimephales promelas (fresh) 96hLC50 180 Wilde, E.W., et al., 1983 

Fish 

Pimephales promelas (fresh) 96hLC50 580 Wilde, E.W., et al., 1983 

Mysid (Sea) 96hLC50 62 Fisher, D.J., et al., 1999 

Dapnia magna (fresh) 96hLC50 32 Fisher, D.J., et al., 1999 

Amphipod (fresh) 96hLC50 78 Fisher, D.J., et al., 1999 

Ceriodaphnia dubia (fresh) 24hLC50 80 Taylor, P.A., 1993 

Crustacea 

Mysidopsis bahia (sea) 96hLC50 73 Fisher, D.J., et al., 1994 

5.4.2.2 Chronic aquatic toxicity 

 Species Effect Value 

(μg/L) Reference 

Fish Menidia peninsulae (sea) 28dNOEC 40 Goodman et al., 1983 

Dreissena polymorpha

(fresh) 11d LC50 1,000 Martin et al. 1993 

Dreissena polymorpha

(fresh) 

20d 

NOEC 500 Martin et al. 1993 

Mollusca 

In a field study on chlorinated condenser cooling effluents using mollusk bivalves 

(Liden et al., 1980), the survival of oysters (Crassostrea virginica) and clams 

(Rangia cuneata) maintained at three TRO concentrations for 15 days was not 

affected at concentration as high as 62 μg/l, while oyster mean shell deposition 

was significantly reduced in the treated animals. At the lowest test concentration 

(14 μg/l) a 14% reduction in shell deposition was observed, so that following TGD 

the NOEC can be estimated as LOEC/2, i.e. 7 μg/l (ESIS,2007) 

Algae Natural algae (fresh) 24dNOEC 79 Pratt et al., 1988 

Community Protozoa and algae NOEC 3 ESIS, 2007 

5.4.2.3 Information on endocrine disruption 

There are no data indicating that sodium hypochlorite has effects on the endocrine of the aquatic 

organisms. 
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5.4.2.4 Sediments toxicity 

Koc of sodium hypochlorite is 14.3 L/kg (EPI SuitTM, v3.20), which is lower than the limit value 

Koc of 500 L/kg. Thus, the substance is not likely to accumulate in sediments and testing with 

sediment dwelling species is not relevant for the assessment. 

5.4.2.5 Bioconcentration/biomagnification 

Log Pow of sodium hypochlorite is -3.42 (EPI SuitTM, v3.20), which is lower than the limited 

Log Pow of 3, indicating a very low potential for Bioconcentration/biomagnification. 

5.4.2.6 Food web/population effects 

Log Pow of sodium hypochlorite is -3.42 (EPI SuitTM, v3.20), which is lower than Log Pow 3 

that is limit value. So the possibility of sodium hypochlorite’s impact to food web and population 

effect should be insignificant. 

5.4.3 Toxic effect on mammals 

5.4.3.1 Acute toxic effect on mammals 

Species Effect Value(g/kg) Reference 

Wistar rats Oral LD50 8.8 ESIS, 2007 

Albino mouse Oral LD50 8.91 ESIS, 2007 

Rabbits Dermal LD0 10 ESIS, 2007 

Mouse Inhalation LD50 10.5 ESIS, 2007 

5.4.3.2 Effects on skin and eye 

 Species Method Results Reference 

Skin Rabbits, 

guinea pigs 

and human 

0.5 ml 12.7% sodium 

hypochlorite, 4 hrs 

Moderate 

irritant 

Nixon, G.A, 

1975 

Eye Rabbits 0.1ml 12.7% sodium 

hypochlorite, 24 hrs 

Severe 

irritation. 

ESIS, 2007 
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5.4.3.3 Repeated-dose toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

Dose 

Species Results Reference 

Oral 90 days 0-250 

mg/L 

Male and 

female 

SpragueDawley rats 

No integrative or regular 

data were observed. 

Daniel et al., 

1990 

Oral 90 days 0-200 

mg/L 

B6C3F1 

Rats 

Water consumption 

obviously decreased. 

Weights of all the mice 

were decreased. 

NOAEL=10mg/kg/d 

Daniel et al., 

1991 

Oral 12 and 

17 weeks 

0.75-1.5 

mg/kg/d 

Rats and mice Pathological changes in 

the immune system were 

detected. 

NTP, 1992 

5.4.3.4 Development and reproductive toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

Dose 

Species Results Reference 

Oral 66-76 

days 

1.0-5.0 

mg 

Cl2/kg/d 

Male and 

female mice 

No Reproductive Toxicity 

was found. NOAEL= 5 

mg/kg/d 

Carlton et al., 

1986 

5.4.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

Dose 

Species Results Reference 

Oral 103 

weeks 

500 or 

1,000 

mg/L 

B6CF1 

mice 

No tumours were observed Sodium 

hypochlorite 

HSDB 

Oral 104 

weeks 

0-2,000 

mg/L 

Male and 

female 

Fischer 

344 rats 

No tumours were observed Sodium 

hypochlorite 

HSDB 

Oral 2 years 0-275 

ppm 

Rats and 

mice 

Leukaemia cases in the female 

mice can not indicate that this 

substance is carcinogenic. 

NTP, 1992 

Oral 104 

weeks 

500 ppm 

or 1,000 

ppm 

female 

and male 

mice 

There was no obvious tumour 

found 

Kurokawa, 

1986 
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5.4.3.6 Toxicokinetics 

The apparent radiochlorine absorption was approximately 65%. Urine was the primary route of 

elimination where 65%-100% of the radio labelled material was the parent chlorate. Chloride was 

the only radiochlorine labelled metabolite detected (MEPC 58/2/2). 

5.4.3.7 Human toxicity 

It is reported that the fatal dose of active chlorine is 200 ml with the concentration of 3%-6% 

(F. Racioppi, et al., 1994). However, there is a record showing that someone had drunk 1L of 

the 5.25% concentration of NaOCl disinfectant and did not die. Another record shows that 

someone had drunk 0.5 L of this disinfectant with the concentration of 10% and also survived 

(Ward and Routlcdge, 1988). Furthermore, it was mentioned in Racioppi’s reports 

that 250 ml-500 ml of the 12.5% concentration of NaClO solution will be sufficient to cause 

death if ingested (Racioppi et al., 1994). And a report from Froner in 1987 shows that a 27-year 

old youngster had drunk 60 ml hypochlorite solution with the injected concentration of 5.25% 

became lethargic, however, after he was revived later, he became safe and sound again as usual. 

At present, the repeated dose of dermal toxicity test for the human body is mainly focused on the 

partial skin exposure. None of the 60 allergic dermatitis patients felt irritation after being coated 

with 1% concentration of NaClO (Habets et al., 1986). 

5.4.4 Environmental fate and effect under aerobic and anaerobic conditions 

 

5.4.4.1 Modes of degradation 

Environment Degradation 

outcome 

Period Results Reference 

Light, rising 

temperature 

chlorate, 

chloridion, 

chlorition 

<1,500 

mins and 

7hrs 

The degradation rate is 

faster in solutions with 

higher concentration. 

M.W. Lister, 

1956; Church, 

1994 

Light, rising 

temperature 

oxygen and 

chloridion 

<1,500 

mins and 

7hrs 

The most active catalysts 

are nickel, cobalt and 

copper. 

M.W. Lister, 

1956; Church, 

1994 

Dark, 

immobile 

 The degradation is in 

accordance with the initial 

reaction kinetics formula, 

i.e. half-life is less 

than 15 minutes. 

Johnson, 

1978 

5.4.4.2 Reactions with the organics 

Due to its high oxidizability, the active chlorine can react with many organics. For example, the 

aquatic natural organics and bromide ion in the water, generating a series of DBPs including 

THMs, HAAs and phenolic compounds. The kind and concentration of substance generated 

depends on the kind of organics and concentration of active chlorine. 
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5.4.4.3 Potential physical effects on wildlife and benthic habitats 

No information is observed that sodium hypochlorite hass effects on wildlife or benthic habitats. 

Considering the extremely low (-3.14) and Koc (14.3) value, this effect can be ignored. 

5.4.4.4 Potential residues in seafood 

Residues of sodium hypochlorite are almost impossible to be found in seafood, because it has no 

bioaccumulation and biomagnification toxicity. 

5.4.5 Testing methods 

Testing method Colorimetric DPD-method 

Applicability Salt water 

Sensitivity 0.02 mg/L Cl2

Reference American Public Health Association, 1989 

5.4.6 Risk characterization 

The PBT criteria identification of sodium hypochlorite are as follows: 

Criteria PBT Criteria Reach the Criteria or 

not 

Persistence Half life 

In seawater>60 days, or in fresh water>40 days, 

or in seawater sediment>180 days, or in fresh 

water sediment>120 days. 

No (refer to 

section 5.4.4.1) 

Enrichment BCF>2,000 or LogP≥3 No (refer to 

section 5.4.1) 

Toxicity Chronic NOEC<0.01 mg/L Yes (refer to 

section 5.4.3.3) 

5.4.7 PNEC/PEC evaluation 

5.4.7.1 PEC evaluation (MAM-PEC) 

MAM-PEC is a user-friendly model of statistics and analysis, which can take different standard 

aquatic scenarios by using different parameters. It is suggested to calculate PEC using this model 

by IMO. The latest version, version 2.0 of MAM-PEC is applied in the study. For more detailed 

information, please refer to the Assessment on Human Exposure Scenario of Ballast Water 

Treated by OceanGuardT M Ballast Water Management System. 

The ballast water discharging capacity of OECD-EU commercial harbour has an exchange 

volume of 51,117,000 m3 (refer to ESD). The daily volume of discharged. treated ballast water is 

simulated as 300,000 m3

/d, according to the description of Port of Rotterdam in 

document MEPC 57/2/7. Concentration of sodium hypochlorite in the discharged ballast water 
MEPC 60/2/8 

ANNEX 

Page 29 

I:\MEPC\60\2-8.doc 

is 0.05 mg/L. After all the physical and chemical properties being inputted, the conclusions 

derived from the software are as follows: 

The result shows the calculated concentration in the Harbour and the Surroundings. The above 

figure shows the definition of Harbour and Surroundings. 

Average concentration of the Harbour: 1.51x10-2 μg/L 

Maximum concentration of the Harbour: 3.27x10-2 μg/L 

Average concentration of the Surroundings: 7.72x10-4 μg/L 

Maximum concentration of the Surroundings: 4.00x10-3 μg/L 

5.4.7.2 PNEC evaluation 

According to the aquatic organism acute toxicity data and aquatic organism chronic toxicity data, 

PNEC is calculated with the lowest value of the data against different species. The impact 

factors are made and corrected according to the Methodology for information gathering and the 

conduct of work of the GESAMP-BWWG. According to the shortest period LC50 of species 

from two different trophic levels, and lowest chronic NOEC of species from several different 

trophic levels, the impact factor is decided to be 50. 

Species Effect Value (μg/L) Minimum Impact 

factor PNEC 

Menidia beryllina (fish/sea) 96hLC50 128 

Mysid (crustacea/sea) 96hLC50 62 

Menidia peninsulae

(fish/sea) 

NOEC (28d) 40 

Dreissena polymorpha

(molluscafresh) 

NOEC (20d) 500 

Crassostrea virginica (sea) NOEC (134 ) 7 

Natural algae (algae/fresh) NOEC (24d) 79 

Community changes NOEC (7d) 3 3 (μg/L) 50 0.06 ug/L 

PEC/PNEC=0.0151/0.06 =0.252<1 

Therefore, this PEC value should be of no harmful effects on the environment when discharging. 
MEPC 60/2/8 

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I:\MEPC\60\2-8.doc 

6 DATA OF THE RELEVANT CHEMICALS IN BALLAST WATER 

6.1 Dibromochloromethane 

6.1.1 Physical and chemical properties of dibromochloromethane 

Property Value Reference 

CAS No. 124-48-1 

Molecular formula CHBr2Cl 

Molecular Weight (g/mol) 208.08 

Structural formula 

Melting point (°C) -20 ATSDR, 2005 

Boiling point (°C) 120 ATSDR, 2005 

Flammability Non-Flammable ATSDR, 2005 

Density (20°C g/cm3) 2.451 ATSDR, 2005 

Vapour pressure (20°C, mmHg) 76 ATSDR, 2005 

Vapour density (air=1) N/A 

water solubility (20°C, g/L) 2.7 ATSDR, 2005 

pH in solution N/A 

Dissociation constant (pKa) N/A 

Oxidation/ reduction potential N/A 

Corrosivity to material or 

equipment 

NO 

Reactivity to container material N/A 

Auto-ignition temperature N/A 

Explosivity N/A 

Oxidizability N/A 

Surface tension N/A 

Viscosity N/A 

Thermal stability and 

decomposition product 

Toxic hydrogen 

bromide gas

Octanol- water partition 

coefficients (log Pow) 

2.16 ATSDR, 2005 

Sediment- water partition 

coefficients (Koc) 

57 ATSDR, 2005 

Henry constant (Pa.m3/mole) 81.0 EPI Suite v3.2 
MEPC 60/2/8 

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6.1.2 Effects on aquatic organisms 

6.1.2.1 Acute aquatic toxicity 

 Species Effect Value 

(mg/L) Reference 

Oryzias latipes (fresh) 96hLC50 79 MEPC 56/2, annex, 

page 9 Fish Cyprinus carpio (fresh) 45minL

C50

52 Mattice, J.S, 1981 

Crustacea Daphnia magna (fresh) 48hEC50 27 MEPC 56/2, annex, 

page 9, 

Tertrahymena pyriformis

(fresh) 

24hLC50 65 MEPC 57/2/1, annex, 

page 17 Algae Selenastrum 

capricornutum (fresh) 

72hEC50 6.1 MEPC 56/2, annex, 

page 9 

6.1.2.2 Chronic aquatic toxicity 

 Species Effect Value (mg/L) Reference 

Cyprinus carpio

(fresh) 

3-5dLC50 33.5 Mattice, J.S, 1981 

Fish Oryzias latipes 

(fresh) 

21dNOE

C 

3.2 MEPC 58/2, annex, page 9 

6.1.2.3 Endocrine toxicity 

There is no information found that dibromochloromethane has effects on the endocrine of aquatic 

species. 

6.1.2.4 Sediment toxicity 

Dibromochloromethane is very stable in the water. The Koc value is 57 L/kg (ATSDR, 2005), 

which is lower than the limit value of 500 L/kg. Thus, the substance is not likely to accumulate 

in sediments and testing with sediment dwelling species is not relevant for the assessment. 

6.1.2.5 Bioconcentration/biomagnification 

Log Pow of sodium dibromochloromethane is 2.16 (EPI SuitTM, v3.20), which is lower than the 

limit of Log Pow 3, indicating a low potential for bioconcentration/biomagnification. 

6.1.2.6 Food web/population effects 

Log Pow of sodium dibromochloromethane is 2.16 (EPI SuitTM, v3.20), which is lower than the 

limited Log Pow of 3, so the possibility of food web/population effects is predicted to be 

insignificant. 
MEPC 60/2/8 

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6.1.3 Toxic effect on mammals 

6.1.3.1 Acute toxic effect on mammals 

Species Effect Value (mg/L) Reference 

Male rat Oral LD50 800 Bowman et al., 1978 

Female rat Oral LD50 1200 Bowman et al., 1978 

Male mouse Oral LD50 916 Chu et al.,1980 

Female 

mouse 

Oral LD50 969 Chu et al.,1980 

Male mouse Oral LD50 2600 Hewitt WR et al.,1983 

6.1.3.2 Effects on skin and eye 

Dibromochloromethane is classified as a skin and eye irritant (MSDS). Whereas, in the NTP 

report, there are no histopathological alterations detected after the 2-year toxicity test on the skins 

and eyes of rats and mice (ATSDR, 2005). 

6.1.3.3 Repeated-dose toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

Dose 

Species Results Reference

Oral 90 

days 

0-200 mg/kg/d SpragueDawley 

rats 

The weight of the testing 

animals decreased, while 

weight of brain, thymus, liver 

and kidney increased. LOAEL 

= 50 mg/kg/d 

Daniel 

FB et al., 

1990 

Oral 14 days 

and 90 

days 

200-300 times 

toxic to human 

beings 

Rats No abnormality was found Balster 

et al., 

1982 

Oral 30 days 100 mg/kg/d 

and 

400 mg/kg/d 

Rats Did not impact the passive 

avoidance of the rats whereas 

obvious toxicity was detected 

with the dose of 400 mg/kg/d. 

Balster 

et al., 

1982 

Oral 14 days 125 mg/kg/day Rats Immunity of the rats was 

decreased 

Munson 

et al., 

1982 

6.1.3.4 Growth and reproductive toxicity 

Exposure Route Oral 

Exposure Duration 6-15 days 

Exposure dose 50-2,000 mg/kg/d 

Species Sprague-Dawley rats 

Results For the group exposed to high dose, the matrix weight decreased 

and toxicity to embryo was caused. 

Reference Ruddick et al.,1983 
MEPC 60/2/8 

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6.1.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

Rapson and Simmon claimed the carcinogenicity of this substance in 1980 and 1978 respectively. 

No other available information about the toxicity of dibromochloromethane was found. 

6.1.3.6 Toxicokinetics 

Dibromochloromethane is lipophilic, and it does not appear to accumulate in adipose tissue. 

It can be absorbed quickly. Two route-independent pathways are thought to metabolize 

it: oxidation by cytochrome P-450 mixed function oxidase system and conjugation via 

glutathione S-transferase. It is primarily excreted via exhalation as the parent compound or 

carbon dioxide (ATSDR, 2005). 

6.1.3.7 Human toxicity 

There is little information about toxicity of dibromochloromethane to human. It is claimed by 

IARC (ATSDR 2005) that dibromochloromethane’s carcinogenicity to human body is not 

classified (Group 3) on the basis of laboratory data at present. Whereas, EPA classified it as 

Group C for it is a potential human carcinogen. 

6.1.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.1.4.1 Modes of degradation (biotic and abiotic) 

Environment Degradation 

period 

Results Reference 

Aerobic, biotic 7 days 10%-25% being 

degraded 

Tabak et al., 1981 

Underground water, 

anaerobic, biotic 

 Half life <50 days Bouwer et al., 1981 

Packed tower, 

anaerobic, biotic 

2 days Removal ratio >99% Bouwer and 

McCarty, 1984 

6.1.4.2 Reactions with organic matters 

The chemical property of dibromochloromethane is very stable, and there is no data indicating its 

capability of reacting with other organic matters. 

6.1.4.3 Potential physical effects on wildlife and benthic habitats 

No data is found to show that dibromochloromethane has effects on wildlife or benthic habitats. 

Considering its low octanol/water partition coefficient (Log Pow value of 2.16) and low 

sediment/water partition coefficients Koc value (57), the effects are slight. 
MEPC 60/2/8 

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I:\MEPC\60\2-8.doc 

6.1.4.4 Potential residues in seafood 

Gotoh, M. et al. had verified in the 1992 report that there were no dibromochloromethane found 

in oysters, clams and sediments of Ariho River and Yoshinaga River. There are no studies about 

the sorption in soil or substances like soil. However, in 2004, Keefe et al. reported that in the 

everglade of nearby sewage outfall in Phoenix and Arizona, the removal rate of 

dibromochloromethane was up to 86.5% thought to be mainly from volatilization. 

6.1.5 Testing method 

Testing method Gas-chromatographic methods 

Applicability Salt water 

Sensitivity 0.5 μg/l 

Reference ISO 10301-F4: 1997 

6.1.6 Risk characterization 

Criteria PBT Criteria Reach the Criteria or 

not 

Persistence Half life 

In seawater >60 days, or in 

fresh water >40 days, or in 

seawater sediment>180 days, 

or in fresh water sediment>120 

days. 

No (refer to 

section 6.1.4.1) 

Enrichment BCF>2,000 or LogP r≥3 No (refer to 

section 6.1.1) 

Toxicity Chronic NOEC>0.01 mg/L No (refer to 

section 6.1.3.3) 

6.1.7 PNEC/PEC evaluation (MAM-PEC) 

6.1.7.1 PNEC evaluation 

Data on the Ecotoxicity of dibromochloromethane is very limited. According to the shortest 

period L(E)C50 of species from three different trophic levels, and lowest chronic NOEC of 

species from one trophic levels, the impact factor is decided to be 1000. 

Species Effect Value 

(mg/L) 

Minimu

m 

Impact 

factor PNEC 

Cyprinus carpio

(fish/fresh) 

45min 

LC50

52 

Daphnia magna

(crustacea/fresh) 48h EC50 27 

Selenastrum 

capricornutum

(algae/fresh) 

72h EC50 6.1 

Oryzias latipes

(fish/fresh) 

21d 

NOEC 3.2 3.2 mg/L 1000 3.2μg/L 
MEPC 60/2/8 

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6.1.7.2 PEC evaluation 

In the discharged ballast water scenario, the maximum value of undiluted concentration 

is 1.7 μg/L, which is already lower than PNEC value, so it is implied that there will be no effects 

on the aquatic environment even if it is undiluted (100%) before discharge. 

6.2 Tribromomethane 

6.2.1 Physical and chemical properties of tribromomethane 

Property Value Reference 

CAS No. 75-25-2 

Molecular formula CHBr3 

Molecular Weight (g/mol) 252.73 

Structural formula 

Melting point (°C) 8.0 ATSDR,2005 

Boiling point (°C) 149.1 ATSDR,2005 

Flammability Non-flammable ATSDR,2005 

Density (20°C g/cm3) 2.899 ATSDR,2005 

Vapour pressure (20°C, mmHg) 5mmHg ATSDR,2005 

Vapour density (air=1) 8.7 ATSDR,2005 

Water solubility (20°C, g/L) 3.1g/L ATSDR,2005 

PH in solution N/A 

Dissociation constant (pKa) N/A 

Oxidation/ reduction potential 2.06V MEPC 56/2/3, 

annex, page 8 

Corrosivity to material or 

equipment 

Reacting with substances of 

strong corrosivity and metal, 

e.g., Sodium hypochlorite, 

sodium, potassium, calcium, 

aluminium powder and zinc. 

IARC, 52 

Reactivity to container material Reacting with some plastic, 

rubber and coatings 

ATSDR,2005 

Auto-ignition temperature N/A 

Explosivity No MSDS 

Oxidizability N/A 

Surface tension 41.53dynes/cm ATSDR,2005 

Viscosity N/A 

Thermal stability and 

decomposition product 

Generating toxicbromine 

hydride gas by pyrolysis

MSDS 

Octanol- water partition 

coefficients (log Pow) 

2.4 ATSDR,2005 

Sediment- water partition 

coefficients (Koc) 

62-126 ATSDR,2005 

Henry constant (Pa.m3/mole) 54.54 Bromoform HSDB 
MEPC 60/2/8 

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6.2.2 Effects on aquatic organisms 

6.2.2.1 Acute toxicity on aquatic organisms 

Species Effect Value (mg/L) Reference 

Cyprinodon variegatus

(sea) 96hLC50 18 Heitmuller et al., 1981 

Lepomis macrochirus

(fresh) 24hLC50 33 Buccafusco et al., 1981 

Lepomis macrochirus

(fresh) 96hLC50 29 Buccafusco et al., 1981 

Fish 

Cyprinodon variegatus

(sea) 96hLC50 7.1 G.S. Ward 

et al.,1981 

Crusta Daphnia magna (fresh) 24hLC50 56 LeBlanc G.A. 1980 

cea Daphnia magna (fresh) 48hLC50 46 LeBlanc G.A. 1980 

Selenastrum 

capricornutum (fresh) 96EC50 28.1 MEPC 56/2/3, annex, 

page 18 Algae Skeletonema costatum

(sea) 96EC50 12.3 MEPC 56/2, 

page 8 

6.2.2.2 Chronic toxicity on aquatic organisms 

 Species Effect Value(mg/L) Reference 

Cyprinodon variegatus(sea) 28dNOEC 4.8 MEPC 57/2/7, annex, 

Fish page 19 

Cyprinodon variegatus(sea) 4dNOEC 2.9 Heitmuller et al., 1981 

Algae Selenastrum capricornutum

(fresh) 4d NOEC 10 MEPC 57/2/8, annex, page 10 

6.2.2.3 Information on production of endocrine disruption 

No evidence shows the effect of tribromothemane on the endocrine disruption of aquatic 

organisms. 

6.2.2.4 Sediment toxicity 

Tribromothemane is relatively stable in water and its degradation rate is very low without the 

existence of bacteria. The Koc value is 62-126 L/kg, which is lower than the maximum limit 

of 500 L/kg, indicating that there is very low possibility for tribromomethane to be adsorbed in 

the sediment and that it has strong mobility. Thus, the substance is not likely to accumulate in 

sediments and testing with sediment dwelling species is not relevant for the assessment. 

6.2.2.5 Bioconcentration/biomagnification 

Log Pow value of tribromomethane is 2.4 (EPI SuitTM, v3.20), which is lower than the limit of 3, 

indicates a low potential for bioconcentration/biomagnification. 
MEPC 60/2/8 

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6.2.2.6 Food web/population effects 

Log Pow value of tribromomethane is 2.16 (EPI SuitTM, v3.20), which is lower than the limit 

of 3, indicates the possibility of food web/population effects would be predicted to be low. 

6.2.3 Toxic effect on mammals 

6.2.3.1 Acute toxic effect on mammals 

Species Effect Value (mg/L) Reference 

ICR Swiss male rats Oral LD50 1.4 (g/kg) Bowman et al., 1978 

ICR Swiss female rats Oral LD50 1.550 (g/kg) Bowman et al.,1978 

Sprague-Dawley male 

rats Oral LD50 1.39 (g/kg) Chu et al., 1980 

Sprague-Dawley female 

rats Oral LD50 1.15 (g/kg) Chu et al., 1980 

Dogs Inhalation 

LC50

7 (mg/L/4h) MEPC 57/2/6, annex 

page 44 

6.2.3.2 Effects on skin and eye 

In NTP report, after being experienced for two years, no tissue changes were observed in the 

skins and eyes of the rats and mice tested (ATSDR, 2005). This substance is classified as a skin 

and eye irritant and sensitizer. It will cause burning and tear for individuals exposed to vapour or 

dust. Repeated contacts with this substance could cause dermatitis in the long term 

(bromoform, HSDB). 

6.2.3.3 Repeated-dose toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

dose 

Species Results Reference

Oral 14 days 50-250 

mg/L 

CD-1 

female 

and 

male 

rats 

In the group taking tribromothemane 

of 250 mg/L, there was decrease in 

the body weight. The weight of liver 

increased, however no change in 

spleen was detected. 

Munson 

et al., 

1982 

Oral 14 days 400 

mg/kg 

and 800 

mg/kg 

Rats 

and 

mice 

Weight of the mice taking the 

400 mg/kg dose decreased by 14%. 

Rats in the 800 mg/kg dose group 

died. 

NTP, 

1989 

Oral 13 weeks 12-200 

mg/kg 

and 200 

mg/kg 

Mice No death observed in the 

12-200mg/kg. No differences 

detected in average weight. 

NOAEL=25 mg/kg NOAEL=50 mg/kg 

NTP, 

1989 

Oral 2 years 100, 200 

mg/kg 

The 

rats and 

mice 

No notable difference was observed 

in the livability or weight. The 

female rats died after 77 weeks. 

NTP, 

1989 

mouth 14 days 145 

mg/kg/d 

Rats Ashen central lobule was observed Condie 

et al., 

1983 
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6.2.3.4 Development and reproductive toxicity 

Exposure 

Duration 

6-15 days 

Exposure dose 0, 50, 100 or 200 mg CHBr3/kg/d 

Species Rats 

Results No maternal toxicity observed; no alteration of litter size or fetal 

weight and incidence of resorptions, but a dose-related increase in 

the incidence of skeletal variations. 

Reference IARC, 52 

6.2.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

In the carcinogenicity study of Fujie, K. in 1993, salmonella was used, the in vitro sister 

chromatid exchange without the S9 activation condition was observed. Also, it was found that 

this was relative to the dose of tribromomethane. 

In the same way, Simmon et al. had concluded the carcinogenicity of tribromomethane by using 

salmonella in 1978. In the documents of Rapson (1980), total contrary conclusions were made. 

Tribromomethane did not show carcinogenicity in Ames test (Rapson W.H., 1980). In the NTP 

report in 1989, it is claimed that tribromomethane did not cause tumour to the rat but intestinal 

cancer caused by tribromomethane was observed in mice. 

In the relevant reports, some are positive while some are negative, so the tribromomethane 

carcinogenicity is difficult to determine. 

6.2.3.6 Toxicokinetic 

Tribromomethane is moderately lipophilic. It does not appear to accumulate in adipose tissue. 

It can be absorbed quickly. Two route-independent pathways are thought to metabolize 

it: oxidation by cytochrome P-450 mixed function oxidase system and conjugation via 

glutathione S-transferase. It is primarily excreted via exhalation as the parent compound or 

carbon dioxide (ATSDR, 2005). 

6.2.3.7 Human toxicity 

Tribromomethane was used as painkiller for children in the early 20th century. The normal dose 

is 180 mg for 3-6 times per day. Few reports had been observed for death by overdose. The 

lethal dose for children is 300 mg/kg claimed by US EPA (WHO EHC 216). 

IARC (IARC 52) assessed the carcinogenicity of tribromomethane and the conclusion was that 

there was no sufficient data of human test. Therefore, this substance is classified as Group 3. 

However, it was classified as Group B2 (possibility of human carcinogenicity) 

by US EPA (IRIS). 
MEPC 60/2/8 

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6.2.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.2.4.1 Modes of degradation 

Environment Degradation 

period 

Results Reference 

Aerobic, biotic 7 days 10%-25% being 

degraded 

Tabak et al., 1981 

Packed tower, anaerobic, 

biotic 

2 days Removal ratio 

>99% 

Bouwer and McCarty, 

1984 

6.2.4.2 Reaction with organic matters 

Tribromomethane is relatively stable, due to its physical and chemical properties. It is not active 

in reacting with organic matters. 

6.2.4.3 Potential physical effects on wildlife and benthic habitats 

No data were observed about the effects on wildlife or benthic habitats, and considering its low 

log Pow value (2.4) and Koc value (62-126), the effects are relatively small. 

6.2.4.4 Potential residues in seafood 

Gotoh, M. et al. verified in the report in 1992 that tribromomethane was not observed in the 

oysters, clams and sediments in Ariho River and Yoshinaga River. Due to its low log Pow and 

Koc value, the bioaccumulation possibility of tribromomethane was determined to be very low. 

6.2.5 Testing methods 

Method Gas-chromatographic methods 

Applicability Salt water 

Sensitivity 0.5 μg/l 

Reference ISO 10301-F4: 1997 

6.2.6 Risk characterization 

Criteria PBT Criteria Reach the Criteria or 

not 

Persistence Half life : 

In seawater>60 days, or in fresh water>40 days, 

or in seawater sediment>180 days, or in fresh 

water sediment>120 days. 

No (refer to 

section 6.2.4.1) 

Enrichment BCF>2,000 or LogP≥3 No (refer to 

section 6.2.1) 

Toxicity Chronic NOEC<0.01 mg/L No (refer to 

section 6.2.3.3) 
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6.2.7 PEC/PNEC evaluation 

6.2.7.1 PEC evaluation (MAM-PEC) 

The ballast water discharging capacity of OECD-EU commercial harbour has an exchange 

volume of 51,117,000m3 (refer to ESD). The daily volume of discharged treated ballast water is 

simulated as 300,000m3

/, which is according to the description of Port of Rotterdam in 

document MEPC 57/2/7. Concentration of tribromomethane in the discharged ballast water 

is 150 μg/L. After all the physical and chemical properties being inputted, the conclusions 

derived from the MAM-PEC software are as follows: 

Average concentration of the Harbor: 9.62x10-1μg/L 

Maximum concentration of the Harbor: 2.62x100

μg/L 

Average concentration of the Surroundings: 2.80x10-2 μg/L 

Maximum concentration of the Surroundings: 1.58x10-1μg/L 

6.2.7.2 PNEC evaluation 

According to the shortest period LC50 of species from three different trophic levels, and lowest 

chronic NOEC of species from two different trophic levels, the impact factor is decided to 

be 500. 

Species Effect Value 

(mg/L) 

Minimum Impact 

factor 

PNEC 

Cyprinodon variegatus (fish/sea) 96hLC50 7.1 

Daphnia magna (crustacea/fresh) 48hLC50 46 

Skeletonema costatum (algae/sea) 96EC50 12.3 

Cyprinodont variegatus (fish/sea) 4dNOEC 2.9 2.9 

(mg/L) 

500 5.8μg/L 

Selenastrum capricornutum

(algae/fresh) 

4d 

NOEC 

10 

PEC/PNEC=0.962/5.8=0.166 <1. 

Therefore, this PEC value indicates no harmful effects to the environment upon discharge. 
MEPC 60/2/8 

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6.3 Dibromoacetic acid 

6.3.1 Physical and chemical properties of dibromoacetic acid (DBAA) 

Property Value Reference 

CAS No. 631-64-1 

Molecular formula C2H2Br2O2 

Molecular Weight (g/mol) 217.84 

Structural formula 

Melting point (°C) 49 WHO,2004 

Boiling point (°C) 242.94 MEPC 58/2, 

annex, page 45 

Flammability 94 MEPC 58/2 

annex, page 45 

Density (20°C, g/cm3) N/A 

Vapour pressure(25°C, Pa) 1.84 MEPC 58/2 

annex, page 45 

Vapour density (air =1) N/A 

Water solubility (25°C, g/L) Diffluent MEPC 58/2 

annex, page 45 

PH in solution N/A 

Dissociation constant (pKa) 1.5 Schultz et al., 1998 

Oxidation/ reduction potential N/A 

Corrosivity to material or 

equipment 

N/A 

Reactivity to container material Store in a tight closed 

container. Store in a cool 

place. Use spark-proof 

tools and explosion-proof 

equipment.

MSDS 

Auto-ignition temperature N/A 

Explosivity Explosive

Oxidizability Oxidizer MSDS 

Surface tension N/A 

Viscosity N/A 

Thermal stability and 

decomposition product 

N/A 

Octanol- water partition 

coefficients (log Pow) 

1.22 WHO,2004 

Sediment- water partition 

coefficients (Koc) 

1.89 EPI Suite v3.2 

Henry constant (Pa.m3/mole) 7.3x10-4 EPI Suite v3.2 

O

OH

Br

Br
MEPC 60/2/8 

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6.3.2 Effects on aquatic organisms 

6.3.2.1 Acute toxicity on aquatic organisms 

Species Effect Value 

(mg/L) 

Reference 

Fish Pimephales promelas(fresh) 96h 

LC50

69 MEPC 58/2 

annex, page 8 

Algae Pseudokirchneriella 

subcapitata (fresh) 

72hEC

50

5.95 ESIS, 2007 

6.3.2.2 Chronic toxicity on aquatic organisms 

No reports indicating that dibromoacetic acid might have any chronic toxicity on aquatic 

organisms were found. 

6.3.2.3 Information on endocrine disruption 

No reports indicating that dibromoacetic acid might have any endocrine effects on aquatic 

organisms were found. 

6.3.2.4 Sediment toxicity 

Dibromoacetic acid’s Koc value is 1.9 L/kg, which is far lower than the maximum limit Koc 

of 500 L/kg. So the possibility of being absorbed in the soil is predicted to be very low. Thus, 

the substance is not likely to accumulate in sediments and testing with sediment dwelling species 

is not relevant for the assessment. 

6.3.2.5 Bioconcentration/biomagnification 

The Log Pow value of dibromoacetic acid is 1.22 (EPI SuitTM, v3.20), which is lower than the 

limit value of 3, indicates a low potential for bioconcentration/biomagnification. 

6.3.2.6 Food web/population effects 

The Log Pow value of dibromoacetic acid is 1.22 (EPI SuitTM, v3.20), which is lower than the 

limit value of 3. Therefore, the possibility of Food web/population effects is predicted to be very 

low. 

6.3.3 Toxic effect on mammals 

6.3.3.1 Acute Toxic effect on mammals 

Species Effect Value 

(mg/L) 

Reference 

Sprague-Dawley Male rats Oral LD50 1.737 Linder et al.,1994 
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6.3.3.2 Effects on skin and eye 

No data was available for the effects on skin and eye. 

6.3.3.3 Repeated-dose toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

Dose 

Species Results Reference 

Oral 3 weeks 0-500 

mg/kg/d 

Male B6C3F1 

rats 

Hepatic weight gained WHO, 

2004 

Oral 2 weeks, 

3 months, 

2 years 

0-270 mg/kg Female and 

male mice. 

Hepatic weight gained. NTP, 2007 

6.3.3.4 Development and reproductive toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

dose 

Species Results Reference 

Oral 8 days 

before the 

gestation 

period 

0-250 

mg/kg/d 

Female 

mice 

No effects on the number of 

implantation sites, pregnancy 

norm or weight of young mice 

were observed 

Cummings 

et al., 1998 

Oral 31 days 0-250 

mg/kg/d 

Male 

mice 

Changes in the sperm form and 

mobility were observed. 

Linder 

et al., 1995 

Oral 14 days 1250 mg 

DBAA/kg/d

Male 

mice 

Blood testosterone was 

decreased, after 14 days returned 

to be normal. 

Linder 

et al., 

1994a 

Oral 14 days 0-279 mg 

DBAA/kg/d

Male 

mice 

In the highest dose group, 

decrease in epididymal sperm 

amount and sperm form 

alteration was observed 

Linder 

et al., 

1994b 

6.3.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

Exposure 

Duration 

2-year 

Species Female and male mice and rats 

Results Increased incidence rate of malignant mesothelioma and monocytic 

leukaemia observed. Liver cell tumour (LCT) and hepatoblastoma 

observed. 

Reference NTP, 2007 

6.3.3.6 Toxicokinetic 

Following gavage exposure in rats, the concentration of DBAA in blood peaked within 1h after 

dosing, suggesting rapid intestinal absorption. It appears to be rapidly excreted. The urine and 

faeces were minimal contributors to overall blood clearance, suggesting biotransformation was 

responsible for the rapid disappearance of DBAA from blood. 
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6.3.3.7 Human toxicity 

Despite there being many animal toxicity laboratory reports, there are few reports on toxicity to 

human, so the toxic effect on mammalian can be used as reference. 

6.3.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.3.4.1 Modes of degradation (biotic and abiotic) 

Holmes et al. tested the degradation rates of DBAA in vivo and vitro. It was reported that the 

half-life is 1.5 hours (MEPC 57/2/7). It is estimated that half-life in the air is 16 days 

(MEPC 57/2/1). 

Mode Half-life Reference 

Biotic 1.5 hrs MEPC 57/2/7, annex, page 24 

Abiotic 16 days MEPC 58/2, annex, page 13 

6.3.4.2 Reaction with organic matters 

No data was available to show its reaction with other organic matters. 

6.3.4.3 Potential physical effects on wildlife and benthic habitats 

No data was available to show its effects on wildlife and benthic habitats. Considering its 

relatively low Log Pow value (1.22) and Koc value (1.89), the effects are predicted to be 

insignificant. 

6.3.4.4 Potential residues in seafood 

Considering its relatively low Log Pow value (1.22) and Koc value (1.89), the possibility of 

potential residues in seafood was predicted to be low. 

6.3.5 Testing methods 

Method Gas-chromatographic methods 

Applicability Salt water 

Sensitivity 0.1-0.5 μg/l 

Reference ISO 23631-2006 
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6.3.6 Risk characterization 

Criteria PBT Criteria Reach the Criteria or not 

Persistence Half life 

In seawater>60 days, or in fresh water>40 days, or in 

seawater sediment>180 days, or in fresh water 

sediment>120 days. 

No 

(refer to 

section 6.3.4.1) 

Enrichment BCF>2,000 or LogP≥3 No (refer to 

section 6.3.1) 

Toxicity Chronic NOEC>0.01 mg/L No (refer to 

section 6.3.3.3) 

6.3.7 PNEC/PEC evaluation 

6.3.7.1 PNEC evaluation 

Documentation of dibromoacetic acid is very limited, so we choose the PNEC value from other 

applications as reference. The PNEC value of 6.9 μg/l in document MEPC 56/2/2 is chosen as 

reference in this application (MEPC 56/2/2, annex, page 40). 

6.3.7.2 PEC evaluation 

In the discharged ballast water scenario, the maximum value of undiluted concentration 

is 5.9 μg/L which is already lower than PNEC value 6.9μg/L, so it is implied that for this 

concentration of dibromoacetic acid, there will be no effects on the aquatic environment even if it 

is undiluted (100%) before being discharged. 

6.4 2,4,6-tribromophenol 

6.4.1 Physical and chemical properties of 2,4,6-tribromophenol 

Property Value Reference 

CAS No. 118-79-6 

Molecular formula C6H3Br3O 

Molecular Weight (g/mol) 330.80 

Structural formula B r O H

B r

B r

Log Kow (estimated): 4.18

Phenol, 2,4,6-tribromoEPI Suite v3.2 

Melting point (°C) 89-96 WHO, 2005b 

Boiling point (°C) 244-290 WHO, 2005b 

Flammability Non-flammable 

Density (20°C, g/cm3) 2.55 MEPC 57/2/6, 

annex, 

page 26 

Vapour pressure (25°C, Pa) 4.2x10-2 WHO, 2005b 

Vapour density (air =1) N/A 

Water solubility (25°C, g/L) 0.059 WHO, 2005b 

PH in solution N/A 

Dissociation constant (pKa) 6.08 WHO, 2005b 

Oxidation/ reduction potential N/A 
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Corrosivity to material or equipment —— 

Reactivity to container material Incompatible materials and strong 

oxidants 

MSDS 

Auto-ignition temperature Non–ignition MSDS 

Explosivity N/A 

Oxidizability N/A 

Surface tension N/A 

Viscosity N/A 

Octanol- water partition coefficients 

(log Pow) 

4.18 EPI Suite v3.2 

Sediment- water partition coefficients 

(Koc) 

1.19x103 EPI Suite v3.2 

Henry constant (Pa.m3/mole) 4.82x10-3 EPI Suite v3.2 

6.4.2 Effects on aquatic organisms 

6.4.2.1 Acute toxicity on aquatic organisms 

 Species Effect Value (mg/L) Reference 

Rainbow trout (fresh) 96hLC50 0.2 WHO, 2005b 

Lepomis macrochirus (fresh) 96hLC50 0.3 WHO, 2005b 

Oryzias latipes (fresh) 96hLC50 1.5 WHO, 2005b 

Pimephales promelas (fresh) 96hLC50 6.3 WHO, 2005b 

Cyprinus carpio (fresh) 96hLC50 1.1 WHO, 2005b 

Fish 

Pimephales promelas (fresh) 8dLC50 4.5 Phipps 

G.L.,1981 

Daphnia magna (fresh) 48hLC50 5.5 WHO, 2005b Crustacea Daphnia magna (fresh) 48hEC50 2.2 WHO, 2005b 

Selenastrum capricornutum

(fresh) 

72hEC50 0.8 WHO, 2005b 

Algae Selenastrum capricornutum

(fresh) 

72hNOEC 0.2 WHO, 2005b 

Protozoa Tetrahymena pyriformis (fresh) 60hEC50 3 WHO, 2005b 

6.4.2.2 Chronic toxicity on aquatic organisms 

 Species Effect Value (mg/L) Reference 

Crustacea Daphnia magna (fresh) 21dNOEC 0.2 WHO, 2005b 

Algae Thalassiosia pseudonana

(sea) 

7dLC50 160 MEPC 57/2/6, annex, 

page 38 

6.4.2.3 Information on endocrine disruption 

No reports were found, indicating that 2,4,6-tribromophenol (2,4,6-TBP) might have any 

endocrine effects on aquatic organisms. 
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6.4.2.4 Sediment toxicity 

The Koc value of 2,4,6-TBP is 1.19x103 L/kg, which is higher than the limit value of 500L/kg. 

If it is released in the water, there will be 93% in water and 7% in soil; if released in the soil, 

there will be 99% absorbed in soil (OECD SIDS), so it has very strong absorption tendency, 

which makes it easy to be absorbed in soil and sediments. 

6.4.2.5 Bioconcentration/biomagnification 

The Log Pow value of 2,4,6-tribromophenol is 4.18, which is higher than the limit value of 3, and the 

substance thus has a potential for bioaccumulation. However, a 28-day exposure test with the fresh 

water fish Lepomis macrochirus (http://www.epa.gov/hpv/pubs/summaries/tribomop/c14177rs.pdf) 

showed a BCF value of only 20. Based on this, 2,4,6-tribromophenol is not likely to accumulate 

in organisms or the food chain. 

6.4.2.6 Food web/population effects 

The Log Pow value of 2,4,6-TBP is 4.18. Available data from fish bioaccumulation studies, and 

also from toxicokinetic studies in rats, indicate that food web effect is not an issue for this 

substance. 

6.4.3 Toxic effect on mammals 

6.4.3.1 Acute toxic effect on mammals 

Species Effect Value(mg/kg) Reference 

Mice Inhalation LC50 >50 (mg/L) WHO, 2005b 

Mice Oral LD50 1486 WHO, 2005b 

Male mice Oral LD50 1995 WHO, 2005b 

Female mice Oral LD50 1819 WHO, 2005b 

Mice Dermal LD50 >2,000 WHO, 2005b 

Rabbits Dermal LD50 >2,000 WHO, 2005b 

6.4.3.2 Effects on skin and eye 

 Species Method Results Reference 

Skin Rabbits and 

mice 

4 h No irritants WHO, 

2005b 

Eye Rabbits 100 mg in 

one 

injection 

Diffuse corneal opacity was 

observed and irritating response 

with moderate conjunctiva burn. 

WHO, 

2005b 
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6.4.3.3 Repeated-dose toxicity 

Exposure Route Oral 

Exposure dose 100, 300 and 1,000 mg 2,4,6-TBP/kg 

Species Female and male mice 

Result The weight decreased seriously. Weight of hepatic and renal gained. 

Decrease in bilirubin and kalium in blood was observed. 

NOAEL 100 mg/kg 

Reference WHO, 2005b 

6.4.3.4 Development and reproductive Toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

dose 

Species Result Reference

Oral 6 to 15 

days 

300 and 

1,000 

mg/kg/d 

Female 

and 

male 

mice 

In the 1,000 mg/kg/d dose group, 

survival ratio and weight of the 

newborn decreased. 

In the 300 mg/kg/d dose group, no 

effect observed. NOAEL for adults, 

1,000 mg/kg/d; 

NOAEL for juvenile. 300 mg/kg/d 

WHO, 

2005b 

Oral 6 to 15 

days 

10-

3,000 mg/kg 

Pregnant 

mouse 

In 1,000 mg/kg and lower dose 

group, decrease in embryo livability 

detected. In 3,000 mg/kg dose 

group, deaths observed. No 

abnormal observed in 300 mg/kg 

dose group. NOAEL, 1,000 mg/kg; 

NOAEL for the pregnant, 300 mg/kg 

WHO, 

2005b 

6.4.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

No data was available for the carcinogenicity/mutagenicity/reproductive toxicity of 2,4,6-TBP. 

6.4.3.6 Toxicokinetic 

From the test of rats, the following results were obtained: 2,4,6-TBP was rapidly absorbed, with 

the concentration in blood peaking after 1hour. The bulk of radioactivity (50%-91%) was rapidly 

excreted via urine, with 4%-14% eliminated in the faeces within 48 hours. The blood 

concentration fell down within 24 hours (WHO, 2005b). 

6.4.3.7 Toxicity on human 

No data was available for the human toxicity. This substance is rapidly absorbed from the 

gastro-intestinal tract and is rapidly excreted via urine and faeces in mammal. 
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6.4.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.4.4.1 Modes of degradation 

Environment Degradation 

products 

Period Results Reference 

Air, light Hydroxyl free 

radicals 

 Half life 34 days WHO, 2005b 

Air, ultraviolet light Hydroxyl free 

radicals 

 Half life 4.6 hrs WHO, 2005b 

Active sludge, aerobic, 

bacteria 

 28 days 49% being decreased WHO, 2005b 

River water 3 days 82% being decreased WHO, 2005b 

Seawater 3 days 9% being decreased WHO, 2005b 

River mouth sediment, 

anaerobic, bacteria 

Phenol <19 days 100% being 

decreased 

Boyle et al., 

1999 

anaerobic, bacteria Phenol Half life 4 days WHO, 2005b 

6.4.4.2 Reaction with organic matters 

No data is available for reaction with organic matters: 2,4,6-TBP is very stable in water, so the 

possibility of reacting with other matters in natural water is predicted to be very low. 

6.4.4.3 Potential effects on wildlife and benthic habitats 

No data is available for its effects on wildlife and benthic habitats. 

6.4.4.4 Potential residues in seafood 

Exposure of bluegills to 2,4,6-TBP for 28 days, plateau levels were reached by 3-7 days of 

exposure. The half-life for residues was less than 24 hours following termination of exposure 

(WHO, 2005b). 

6.4.5 Testing methods 

Method Gas-chromatographic methods 

Applicability Salt water 

Sensitivity 0.1μg/l 

Reference DIN-EN 12673: 1999 
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6.4.6 Risk characterization 

Criteria PBT Criteria Reach the Criteria or not 

Persistence Half life 

In seawater>60 days, or in fresh water>40 

days, or in seawater sediment>180 days, or in 

fresh water sediment>120 days. 

No (refer to section 6.4.4.1) 

Enrichment BCF> 2,000 or LogP≥3 No (refer to section 6.4.2.5) 

Toxicity Chronic NOEC<0.01 mg/L No (refer to section 6.4.3.3) 

6.4.7 PNEC/PEC evaluation 

6.4.7.1 PNEC evaluation 

According to the shortest period L(E)C50 of species from two different trophic levels, and lowest 

chronic NOEC of species from two different trophic levels, the impact factor is decided to 

be 500. 

Species Effect Value 

(mg/L) 

Minimum Impact 

factor

PNEC

Rainbow trout (fish/fresh) 96hLC50 0.2 

Daphnia magna (crustacea/fresh) 48hEC50 2.2 

Selenastrum capricornutum

(algae/fresh) 

72hNOEC 0.2 

Daphnia magna (crustacea/fresh) 21dNOEC 0.2 

0.2 

(mg/L) 

500 0.4 

μg/L 

6.4.7.2 PEC evaluation 

In the discharged ballast water scenario, the maximum value of undiluted concentration 

is 0.1 μg/L, which is already lower than PNEC value 0.4μg/L, so it implies that for this 

concentration of 2,4,6- TBP, there will be no effects on the aquatic environment even if it is 

undiluted (100%) before being discharged. 

6.5 Bromate ion 

6.5.1 Physical and chemical properties of potassium bromate 

Property Value Reference 

CAS No. 7758-01-2 

Molecular formula KBrO3 

Molecular Weight (g/mol) 167 

Structural formula 

Melting point (°C) 350 WHO, 2005 

Boiling point (°C) 370 WHO, 2005 

Flammability Non-Flammable ICSC:1115 

Density (20°C g/cm3) 3.27 WHO, 2005 
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Vapour pressure (20°C, Pa) N/A 

Vapour density (air =1) 5.8 MEPC 56/2/3, 

annex, page 8 

Water solubility (40°C, g/L) 133 WHO, 2005 

PH in solution N/A 

Dissociation constant (pKa) 0.7(HBrO3) EHC,216 

Oxidation/reduction potential N/A 

Corrosivity to material or 

equipment 

Corrosive MEPC 56/2/3, 

annex, page 8 

Reactivity to container material No touching with flammable 

and reductive substances 

ICSC:1115 

Auto-ignition temperature N/A 

Explosivity Explosion may be caused by 

heating. Sensitive with 

mechanical impact. 

MSDS 

Oxidizability Strong oxidizer ICSC:1115 

Surface tension N/A 

Viscosity 66.6-67.6 MEPC 56/2/3, 

annex, page 8 

Thermal stability and 

decomposition product 

N/A 

Octanol- water partition 

coefficients (log Pow) 

-7.18 EPI Suite v3.2 

Sediment- water partition 

coefficients (Koc) 

35 EPI Suite v3.2 

Henry constant (Pa.m3/mole) 0.85 MAM-PEC V2.0 

6.5.2 Effects on aquatic organisms 

6.5.2.1 Acute toxicity on aquatic organisms 

 Species Effect Value (mg/L) Reference 

Oncorhynchus keta (fresh) 96hLC50 512 MEPC 56/2/3, annex, 

page 16 

Saltwater fish (sea) 96hLC50 427-512 Thomas H., 1997 Fish 

Saltwater fish lavae (sea) 96hLC50 31 Thomas H., 1997 

Daphnia magna (fresh) 48 hLC50 179 Thomas H., 1997 

Crustacea Polycelis nigra (fresh) 48hLC50 2258 Thomas H., 1997 

Mysid shrimp (sea) 24hLC50 176 Thomas H., 1997 
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6.5.2.2 Chronic toxicity on aquatic organisms 

 Species Effect Value (mg/L) Reference 

Fish N/A 

Crustacea N/A 

Algae Unknown (sea) EC50 >13.6 Tomas H.,1997 

6.5.2.3 Information on endocrine disruption 

No reports indicating that bromate ion might have any endocrine effects on aquatic organisms 

were found. 

6.5.2.4 Sediment toxicity 

Bromate ion is inorganic ion with the Log Pow of -7.18, which is lower than the limit value of 3, 

and the Koc is 35 l/kg, which is also lower than the limit value of 500 l/kg. It is indicated that the 

possibility for potassium bromate being absorbed in the soil is very low and it has strong 

mobility. Thus, the substance is not likely to accumulate in sediments and testing with sediment 

dwelling species is not relevant for the assessment. 

6.5.2.5 Bioavailability/bioconcentration/biomagnification 

The Log Pow value of potassium bromate is -7.18 (EPI SuitTM, v3.20), which is lower than the 

limit value of 3. Therefore, the potential for bioconcentration/biomagnification is insignificant. 

6.5.2.6 Food web/population effects 

The Log Pow value of potassium bromate is -7.18 (EPI SuitTM, v3.20), which is lower than the 

limit value of 3. Therefore, the possibility of effects on food web/population effects is predicted 

to be low. 

6.5.3 Toxic effect on mammals 

6.5.3.1 Acute toxic effect on mammals 

Species Effect Value 

(mg/L) 

Reference 

F344 male mouse Oral LD50 400 Kurokawa et al., 1990 

F344 female mouse Oral LD50 495 Kurokawa et al., 1990 

B6C3F1 male rat Oral LD50 280 Kurokawa et al., 1990 

B6C3F1 female rat Oral LD50 355 Kurokawa et al., 1990 

Syrian golden male hamster Oral LD50 388 Kurokawa et al., 1990 

Syrian golden female hamster Oral LD50 460 Kurokawa et al., 1990 
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6.5.3.2 Effects on skin and eye 

 Main symptom Result Reference 

Skin Redness, stinging and pain to the 

skin. The skin will be slightly 

burned after a long time. 

Irritant MSDS 

Eye Redness, pain and damage Irritant to 

eyes 

MSDS 

6.5.3.3 Repeated-dose toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

dose 

Species Results Reference 

Oral 15 weeks 30 mg/kg/d Mice NOAEL=30 mg/kg/d MEPC 56/2/3 

Oral 2 weeks 0-540 

mg/kg/d 

Male SPF 

rats 

Decrease in weight was 

observed in the high dose 

group. Weight of kidney, 

lung and liver increased. 

NOAEL=107 g/kg/d 

WHO, 2005 

Oral 13 weeks 150-10,000 

ppm 

Female and 

male F344 

mice 

All animals taking the dose of 

>1250ppm died. Animals 

taking the dose of <600ppm 

all survived, and weight 

suppression was observed. 

Kurokawa 

et al., 1986 

Oral 78 weeks 0-91.6 mg 

kg/d 

Female 

B6C3F1 

rats 

No side-effects. Kurokawa 

et al., 1986 

Oral 4 and 8 

and 12 

weeks 

75 ppm Mice, dogs 

and 

monkeys 

No side-effects WHO, 2005a 

Oral 15 

months 

30 mg/kg/d Male 

Wistar 

mice 

Development suppressions 

were observed. Sponge 

kidney, nitrogen increased and 

abnormal structure of renal 

tubes were caused. 

LOAEL=30mg/kg/d 

WHO, 2005a 

Oral 100 

weeks 

0-28.7 

mg/kg/d 

Female and 

male F344 

mice 

Death and weight gain were 

observed in male mice of 

highest dose group. 

NOAEL=1.1 mg/kg/d 

WHO, 2005a 

Oral 100 

weeks 

0, 6.9, 32.5 

and 59.6 

mg/kg/d 

B6C3F1 

rats 

No changes were observed. 

NOAEL=59.6 mg BrO3

—/kg/d 

WHO, 2005a 
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6.5.3.4 Development and reproductive toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

dose 

Species Results Reference 

Oral 0-250 ppm Female and 

male SpragueDawley rats 

Only a little sperm 

number decrease of 

epididymides were 

observed. NOAEL=80 

ppm 

NTP, 1996, 

abstract for 

RDGT9400 

Oral 10 months 14 ppm and 

100 ppm 

Female and 

male mice 

No changes were 

observed. 

Kurokawa, 

1990 

6.5.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

Exposure 

Route 

Exposure 

Duration 

Exposure 

dose 

Species Results Reference 

Oral 110 

weeks 

500 and 

250 ppm 

Female 

and male 

mice 

Not only cause renal carcinoma to 

the mice but also peritoneal 

mesothelioma to the male mice 

Kurokawa, 

1986 

Fills the 

stomach 

78-104 

weeks 

500-

1,000 

ppm 

Female 

and 

male 

F344 

mice 

For the 1,000 ppm dose group, lung 

cancer, liver cancer and lymphoma 

were observed. For the 600 mg/kg 

group, one renal carcinoma case 

was observed. 

Kurokawa, 

1990 

Oral 24 hrs 167-501 

mg/kg 

Mice Dramatically increase of 

intraosseous chromosome 

aberration rate was observed and 

the value decreased in 24 hours. 

Fujie, 1988 

6.5.3.6 Toxicokinetic 

There were some tests reports about the kinetics and metabolism in animals and humans, though 

different results were concluded. Following oral administration, bromate is absorbed from the 

gastrointestinal tract in both humans and animals. Bromate is excreted mainly in the urine, partly 

as bromate and partly as bromide (WHO, 2005a). 

6.5.3.7 Toxicity on human 

Potassium bromate can cause naupathia, vomiting, bellyache, diarrhea, anuria and centrum 

neurothlipsis, hemolytic anemia, hydropneumonia of varied degrees, etc. Most of these 

symptoms were reversible. After taking the dose of 240-500 mg/kg/d, renal failure and deafness 

may be caused, some of which may be irriversible (WHO, 2005). 

According to the massive outcomes in animal tests, potassium bromate is classified as Group 2B 

by IARC (IARC Supplement 7) (possibility of carcinogenicity to human). 
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6.5.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.5.4.1 Modes of degradation 

Environment Route Degradation 

outcome 

Results Reference 

Water React with 

substances with 

reducibility, 

including metal and 

organics. 

bromide ion Half-life 

12 hours 

MEPC 56/2/3, 

annex, page 20 

6.5.4.2 Reaction with organic matters 

As described in WHO (2005) documents, bromate is not a volatile substance, and it can be 

absorbed in the soil and sediments only in slight amount. It can react with many organic matters 

and produce bromate ion. 

6.5.4.3 Potential physical effects on wildlife and benthic habitats 

No data is available for the potential physical effects on wildlife and benthic habitats. 

Considering its relatively low Log Pow of -7.18, and Koc of 35 L/kg, the effects are predicted to 

be insignificant. 

6.5.4.4 Potential residues in seafood 

Because of its low Log Pow of -7.18 and Koc of 35 L/kg, the possibility of bioaccumulation is 

insignificant, and it is assumed to be no residues in seafood. 

6.5.5 Testing methods 

Method IC-ICP-MS technique 

Applicability Salt water 

Sensitivity 1μg/l 

6.5.6 Risk characterization 

Criteria PBT Criteria Reach the Criteria or not 

Persistence Half life 

In seawater > 60 days, or 

in fresh water> 40 days, or in 

seawater sediment>180 days, 

or in fresh water sediment>120 

days. 

No (refer to section 

6.5.4.1) 

Enrichment BCF>2,000 or LogP ≥ 3 No (refer to section 6.5.1) 

Toxicity Chronic NOEC<0.01 mg/L No (refer to section 

6.5.3.3) 
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6.5.7 PNEC/PEC evaluation 

6.5.7.1 PNEC evaluation 

Toxicity data of bromate is limited. According to the shortest period LC50 of species from two 

different trophic levels, and lowest chronic NOEC of species from two different trophic levels, 

the impact factor is decided to be 5000. 

Species Effect Value 

(mg/L) 

Minimum Impact 

factor 

PNEC 

Saltwater fish lavae 

(fish/seawater) 

96hLC50 31 31 (mg/L) 5000 6.2 μg/l 

Mysid shrimp 

(crustacea/seawater) 

24hLC50 176 

6.5.7.2 PEC evaluation 

In the simulated discharged ballast water (refer to section 3.5, NIVA report), the maximum value 

of undiluted concentration is 3.5μg/L which is already lower than PNEC value 6.2 μg/L, so it 

implies that for the ballast water with this concentration of bromate ion, there will be no effects 

on the aquatic environment even if it is undiluted (100%) before being discharged. 

6.6 Carbon monoxide 

6.6.1 Physical and chemical properties of carbon monoxide 

Property Value Reference 

CAS No. 630-08-0 

Molecular formula CO 

Molecular weight (g/mol) 28.01 

Structural formula C-O 

Melting point (°C) -205 Carbon monoxide HSDB 

Boiling point (°C) -191.5 Carbon monoxide HSDB 

Flammability Flammable; react 

with oxygen 

Density (0°C, g/l) 1.25 Carbon monoxide HSDB 

Vapour pressure (20°C, Pa) > 1 atm Carbon monoxide HSDB 

Vapour density (air =1) 0.968 Carbon monoxide HSDB 

Solubility in water (20°C, g/l) Slight, 2.3ml/100cc Carbon monoxide HSDB 

PH in solution N/A 

Dissociation constant (pKa) N/A 

Oxidation/reduction potential N/A 

Corrosivity to material or 

equipment 

No 

Reactivity to container 

material 

No reaction in 

normal condition 

MSDS 
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Auto-ignition Temperature 

(°C) 

639°C MSDS 

Explosivity It may explode 

when heated 

Carbon monoxide OSHA 

Oxidizability Yes 

Surface tension 9.8 mN/m Carbon monoxide HSDB 

Viscosity 16.62 uN s/sq m Carbon monoxide HSDB 

Thermal stability and 

decomposition product 

decompose into 

carbon and carbon 

dioxide at 400-

700°C 

Carbon monoxide HSDB 

Octanol-water partition 

coefficients (Log Pow) 

 

Sediment-water partition 

coefficients (Koc) 

 

Henry constant (Pa.m3/mole) 

6.6.2 Effects on aquatic organisms 

6.6.2.1 Acute aquatic toxicity 

There are no data indicating that carbon monoxide has acute aquatic toxicity. 

6.6.2.2 Chronic aquatic toxicity 

There are no data indicating that carbon monoxide has chronic aquatic toxicity. 

6.6.2.3 Information on endocrine disruption 

There are no relevant data available. 

6.6.2.4 Sediments toxicity 

There are no relevant data available. 

6.6.2.5 Bioconcentration/biomagnification 

There are no relevant data available. 

6.6.2.6 Food web/population effects 

When carbon monoxide is inhaled, the body will possibly die because of absence of oxygen. It 

does not have a potential for bioconcentration/biomagnification, so the possibility of food 

web/population effects is negligible. 
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6.6.3 Toxic effect on mammals 

6.6.3.1 Acute toxic effect on mammals 

Species Effect Value(ppm) Reference 

Rats Inhalation LC50 1807 Carbon monoxide OSHA 

6.6.3.2 Effects on skin and eye 

Inhalation is the main exposure route. It causes no skin toxicity and no effect on skin or eyes 

either. 

6.6.3.3 Repeated-dose toxicity 

Exposure 

route 

Duration Dose Species Method Results Reference

Inhalation 6 

weeks 

57 and 110 

mg/m3

Dogs Intermittently 

or 

continuously 

Abnormal 

electrocardiograms 

EHC 213 

Inhalation 14 

months 

570 mg/m3 

(500 ppm) 

Monkeys Continuously No effects on the 

electrocardiogram 

EHC 213 

Inhalation 38-47 

days 

570 mg/m3

(500 ppm) 

Rats Continuously Heart weight to 

body weight ratios 

increased 

EHC 213 

6.6.3.4 Development and reproductive toxicity 

Exposure 

route 

Duration Dose Species Method Results Reference

Inhalation Last 18 days 

of gestation 

230 

mg/m3

Rats Continuously Decrease in litter size 

and birth weights 

EHC 213 

Inhalation Continuously 

through 

gestation 

210 

mg/m3

Rabbits Continuously Increase in fetal 

mortality; 

malformations 

EHC 213 

6.6.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

No relevant data are available. 

6.6.3.6 Toxicokinetic 

It can combine with haemoglobin to produce carboxyhaemoglobin, decreasing the 

oxygen-carrying capacity of blood and interfering with oxygen release at the tissue level. 

Hypoxia of sensitive tissues can affect the function of many organs, including the lungs 

(EHC 213). 
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6.6.3.7 Human toxicity 

Inhalation of carbon monoxide causes tissue hypoxia by preventing the blood from carrying 

sufficient oxygen. It combines reversibly with hemoglobin to from carboxyhemoglobin. Acute 

exposure may cause headache, flushing, nausea, vertigo, weakness, irritability and 

unconsciousness. Chronic exposure can cause persistent sighs and symptoms, such as anorexia, 

headache, lassitude and ataxia. 

Healthy young men exposed to carbon monoxide at a concentration of 44 ppm for a prolonged 

period suffered no adverse health effects. Men exposed to 50 ppm for several days without relief 

complained of headaches, but exposure to 40 ppm for 60 days was without effect. Workers in the 

Holland Tunnel working 8-hour wing shifts of 2 hours in and 2 hours out at an average carbon 

monoxide exposure concentration of 70 ppm had average carboxyhemoglobin levels of 5 percent, 

and none had levels above 10 percent (carbon monoxide OSHA). 

6.6.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.6.4.1 Modes of degradation 

Carbon monoxide exists in nature. It is a product of the incomplete combustion of 

carbon-containing fuels. It has small solubility in water. But it can react with other chemicals by 

photolysis. The average atmospheric lifetime of carbon monoxide can be calculated to be 

about 2 months, with a range between 1 and 4 months, which can vary enormously with latitude 

and season (EHC 213). 

6.6.4.2 Reactions with the organic matters 

There is no data indicating its capability of reacting with other organic matters. 

6.6.4.3 Potential physical effects on wildlife and benthic habitats 

No relevant data are available. 

6.6.4.4 Potential residues in seafood 

Since carbon monoxide has no effect on bioconcentration, it is impossible to have residue in seafood. 

6.6.5 Analytical method 

The gas concentration of carbon monoxide was measured by handheld gas sensors. 

6.6.6 Risk characterization 

Criteria PBT Criteria Reach the Criteria or 

not 

Persistence Half-life: 

>60 days in marine water, or >40 days in fresh water, or 

>180 days in marine sediments, or >120 days in fresh 

water sediments 

No (low solubility in 

water) 

Enrichment BCF >2,000 or LogP ≥3 No (refer to section 

6.6.2.5) 

Toxicity Chronic NOEC<0.01 mg/L No (refer to section 

6.6.3.3) 
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6.7 Methane 

6.7.1 Physical and chemical properties of methane 

Property value reference 

CAS No. 74-82-8 

Molecular formula CH4 

Molecular weight(g/mol) 16.05 

Structural formula 

Melting point (°C) -183 Methane OSHA 

Boiling point (°C) -161.5 MSDS 

Flammability yes 

Density (0°C, g/l) 0.55 MSDS 

Vapour pressure (mmHg, 37.8C) 258574 Methane OSHA 

Vapour density (air =1) N/A 

Solubility in water (20°C, g/l) negligible MSDS 

PH in solution N/A 

Dissociation constant (pKa) N/A 

Oxidation/reduction potential N/A 

Corrosivity to material or 

equipment 

No 

Reactivity to container material No touch with oxidizer 

Auto-ignition Temperature (°C) 580 MSDS 

Explosivity Reaction with oxygen may 

cause explode 

Oxidizability No 

Surface tension N/A 

Viscosity N/A 

Thermal stability and 

decomposition product 

decompose into carbon and 

hydrogen under high 

temperature (>1,000°C) 

without oxygen 

Octanol-water partition 

coefficients (Log Pow) 

 

Sediment-water partition 

coefficients (Koc) 

 

Henry constant (Pa.m3/mole) 

6.7.2 Effects on aquatic organisms 

6.7.2.1 Acute aquatic toxicity 

There are no data indicating that methane has acute aquatic toxicity. 
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6.7.2.2 Chronic aquatic toxicity 

There are no data indicating that methane has chronic aquatic toxicity. 

6.7.2.3 Information on endocrine disruption 

No relevant data are available. 

6.7.2.4 Sediment toxicity 

No relevant data are available. 

6.7.2.5 Bioconcentration/biomagnification 

Methane is a simple asphyxiant. It can cause asphyxia in high concentration. It has a very low 

potential for bioconcentration/biomagnification. 

6.7.2.6 Food web/population effects 

Due to a low potential for bioconcentration/biomagnification, the possibility of food 

web/population effects is negligible. 

6.7.3 Toxic effect on mammals 

6.7.3.1 Acute toxic effect on mammals 

No report in detail is relevant with acute toxic effect on mammalian. The main exposure route is 

inhalation. The body will possibly be unconscious or die because of the absence of oxygen in 

high concentration. 

6.7.3.2 Effects on skin and eye 

It is not stimulated in ACGIH (7th, 2001), it was carried out outside the category for both skin 

and eye (MSDS). 

6.7.3.3 Repeated-dose toxicity 

No relevant data are available. 

6.7.3.4 Development and reproductive toxicity 

Oxygen deficiency during pregnancy has produced developmental abnormalities in humans and 

experimental animals (MSDS). 

6.7.3.5 Carcinogenicity/mutagenicity/reproductive toxicity 

No relevant data are available. 
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6.7.3.6 Human toxicity 

Methane is a simple asphyxiant. Effects of oxygen deficiency resulting from simple asphyxiants 

may include rapid breathing, diminished mental alertness, impaired muscular coordination, faulty 

judgement, depression of all sensations, emotional instability, and fatigue. As asphyxiation 

progresses, nausea, vomiting, prostration, and loss of consciousness may result, eventually 

leading to convulsions, coma and death (MSDS). 

6.7.4 Environmental fate and effect under aerobic and anaerobic conditions 

6.7.4.1 Modes of degradation 

No relevant data is available. 

6.7.4.2 Reactions with the organic matters 

There is no data indicating its capability of reacting with other organic matters in nature. 

6.7.4.3 Potential physical effects on wildlife and benthic habitats 

No relevant data is available. 

6.7.4.4 Potential residues in seafood 

Methane is unlikely to be present as a residue in seafood. 

6.7.5 Analytical method 

The gas concentration of methane was measured by handheld gas sensors. 

6.7.6 Risk characterization 

Criteria PBT Criteria Reach the 

Criteria or not 

Persistence Half-life: 

>60 days in marine water, or >40 days in fresh 

water, or >180 days in marine sediments, or >120 

days in fresh water sediments 

No (negligible 

solubility in 

water) 

Enrichment BCF>2,000 or LogP ≥3 No (refer to 

section 6.7.2.5) 

Toxicity Chronic NOEC<0.01 mg/L No (MSDS) 
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7 TOXICITY ASSESSMENT OF THE TREATED BALLAST WATER 

Toxicity tests for the treated ballast water of OceanGuardTM Ballast Water Management System 

was carried out at NIVA, including Active Substances and Relevant Chemicals in the discharged 

water, and the toxicity of the discharged water. 

The 1 mg/L concentration was chosen for full toxicity testing of seawater. Water treated with 

initial TRO concentrations of 2 mg/L and 4 mg/L, was only tested with respect to algae toxicity. 

The 4 mg/L concentration was chosen for full toxicity testing of brackish water, based on the 

rapid decay of TRO in brackish water and low concentrations of TRO measured on day 5. The 

test concentrations of 1 mg/L and 2 mg/L in brackish water were only tested with respect to algae 

toxicity. The two initial TRO concentrations are selected on the basis of the biological efficacy 

outcome and the TRO degradation condition. However, since the initial TRO of 2 mg/L in 

brackish water testing has reached the optimum of the balance between biological efficacy and 

toxicity, 2 mg/L and 1 mg/L will be chosen for the following tests with brackish water (22 PSU) 

and seawater respectively. 

Since the ecotoxicological responses to emission scenario are caused mostly by TRO, so the 

TRO concentration has been measured timely in fixed point during the test. 

7.1 Contents of oxidants 

Figure 7.1 : Column diagram of varied initial TRO degrading with time 

in seawater (33 PSU) (refer to section 3.4, NIVA report) 

Note the part in blue colour shows the results of the selected testing cycle. In this cycle, TRO 

concentration of treated seawater is below 0.2 mg/L after one day storage. 
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Figure 7.2 : Column diagram of varied initial TRO degrading with time 

in brackish water (22 PSU) (refer to section 3.4, NIVA report) 

Note the part in yellow colour shows the results of the selected testing cycle. In this cycle, TRO 

concentration of treated brackish water is below 0.2 mg/L after one day storage. 

During the tests, the TRO concentration was measured every day at the same time for 5 days. 

The degradation progress of TRO in different test waters can be seen in figures 7.1 and 7.2. 

Initial TRO levels were set at 1, 2 and 4 mg/L for the two different waters. The red dashed line 

in the figure indicates that the TRO concentration of 0.2 mg/L after 5 days as suggested by the 

GESAMP-BWWG (Ref. 0.1-0.2 mg/L, Report of the seventh meeting of the GESAMP Ballast 

Water Working Group, MEPC 58/2/8). 

According to figures 7.1 and 7.2, TRO concentration of seawater (33 PSU) and brackish water 

(22 PSU) treated by 1 mg/L and 2 mg/L initial TRO, is all below 0.2 mg/L. Presuming this 

system is installed on vessels with short voyage period, the TRO of treated ballast water before 

discharge can meet the requirement, without the need of adopting the TRO neutralization 

equipment. 

7.2 Determination of holding time 

After the treatment of the EUT unit, there is 1-2 mg/L Cl2 TRO existing in the treated water for 

some time, and there is a certain degradation mode for the TRO. In order to determine the 

degradation of TRO, samples were taken everyday (refer to figure 7.1). TRO concentrations of 

seawater (33 PSU) and brackish water (22 PSU) treated by 1 mg/L and 2 mg/L initial TRO, 

respectively, are below 0.2 mg/L on Day 1, (i.e. with the TC of 0.14 mg/L and 0.09 mg/L 

respectively), and the FC of 0.08 mg/L and 0.04 mg/L, respectively. On day 3, the TRO 

concentration is stable, with the TC of 0.07mg/L and 0.04 mg/L, respectively, and the FC 

of 0.04 mg/L and <0.02 mg/L, respectively (refer to section 3.4, NIVA report). So the 

determination of holding time is 3 days. 
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The fast degradation rate of TRO is in the first 3 days. The degradation ratio is more than 95% in 

the first 3 days. From day 3 to day 5, the degradation slows down. There is no significant 

difference between the TRO concentration of day 3 and day 5. 

Toxicity tests have been carried out for the treated water, sampled on day 5. According to the 

results, there is residual ecotoxicity of 33 PSU seawater treated with the 1 mg/L initial TRO, 

however, after dilution to some extent, it is safe to discharge to the environment around. No 

ecotoxicity will be caused by the 22 PSU brackish water treated by the 2 mg/L initial TRO 

(refer to section 3.7, NIVA report). So, the suggested holding time is 3 days. 

7.3 Ecotoxicity 

Toxicity tests were carried out on the algae, invertebrate and fish. The 1 mg/L concentration was 

chosen for full toxicity testing of seawater. The test concentrations of 2 mg/L and 4 mg/L TRO 

were only tested with respect to marine algal growth inhibition. The 4 mg/L concentration was 

chosen for full toxicity testing of brackish water. The test concentrations of 1 mg/L and 2 mg/L 

in brackish water were only tested with respect to algae toxicity. See outcomes in the figures 

below (refer to figure 1, NIVA report). 

1

10

100

1000

0 20 40 60 80

hours

106 cells/l

Cont rol

32

56

100

Figure 7.3 : Algae growth curve for 100, 56 and 32% of 33 PSU seawater treated 

by 1 mg/L initial TRO, sampled on day 5 

In the treated seawater (33 PSU) with the initial TRO concentration of 1 mg/L, after being 

diluted in varied multiples of 32%, 56% and 100% (undiluted), respectively, no absolute effects 

on the growth of algae were observed. For the 32% concentration, the normal growth of algae 

was not affected, while for the 56% and 100% concentrations, algae was not killed, however, the 

growth was inhibited by different degrees. So the simulated ballast water can cause no effects on 

the most sensitive algae by being diluted 3-4 times. 
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Table 7.1 : Ecotoxicity tests performed on treated seawater (33 PSU), sampled on day 5 

Results are presented as percentage (%) of treated ballast water. Dilution water is non-treated 

ballast water (refer to Table 18, NIVA report). 

Test Species Test Result 

Marine algae growth 

inhibition 

1 mg/L 

Skeletonema costatum EC10 = 92% 

EC50 = >100% 

Marine algae growth 

inhibition 

2 mg/L 

Skeletonema costatum EC50 = 33% 

EC10 = 30% 

Marine algae growth 

inhibition 

4 mg/L 

Skeletonema costatum EC50 = 18% 

EC10 = 11% 

Acute invertebrate 

1 mg/L 

Acartia tonsa LC50 = >100% 

NOEC = 56% 

Acute fish test 

1 mg/L 

Scopthalmus maximus LC50 = >100% 

NOEC = ≥ 100% 

Table 7.1 shows the toxicity data of different initial TRO concentrations. In the water treated by 

the initial TRO of 1 mg/L, EC50 and LC50 levels are not reached even for the undiluted water, 

indicating that water can be discharged directly with no significant toxicity to the environment. 

It is observed that toxicity of water, treated by the initial TRO of 2 mg/L and 4 mg/L, is 

obviously greater than that of 1 mg/L and the linear relation with the TRO initial concentration is 

shown (refer to Table 8, NIVA report). 

1

10

100

1000

10000

0 20 40 60 80

Hours

106 cells/l

Control

32

56

100

Concentration

%

Figure 7.4 : Algae growth curves for 100, 56 and 32% of 4 ppm TRO in 22 PSU brackish 

water treated by 2 mg/L initial TRO, sampled on day 5 
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In the treated salt water (22 PSU) with the initial TRO of 2 mg/L, after being diluted in varied 

multiples of 32%, 56% and 100% (undiluted), respectively, no absolute effects on the growth of 

algae were observed. For the 32% and 56% concentrations, the normal growth of algae was not 

affected, while for the 100% concentration, light inhibition on the algae growth is observed. 

Thus, 2 mg/L is selected as the initial TRO level, and the effects on organisms will not be 

significant after few multiple dilution of the emission. 

Table 7.2 : Ecotoxicity test performed on treated brackish water (22 PSU). 

Results are presented as percentage (%) of treated ballast water. Dilution water is non-treated 

ballast water (refer to Table 19, NIVA report). 

Test Species Test Result 

Marine algae growth inhibition 

1 mg/L 

Skeletonema costatum EC50 = >100% 

EC10 = ≥ 100% 

Marine algae growth inhibition 

2 mg/L 

Skeletonema costatum EC50 = >100% 

EC10 = ≥ 100% 

Marine algae growth inhibition 

4 mg/L 

Skeletonema costatum EC50 = >100% 

EC10 = 82% 

Acute invertebrate 

4 mg/L 

Acartia tonsa LC50 = >100% 

NOEC = ≥ 100% 

Acute fish test 

4 mg/L 

Scopthalmus maximus LC50 = >100% 

NOEC = ≥ 100% 

The toxicity of treated brackish water is to some extent in line with the concentration of initial 

TRO. No ecotoxicity will be caused by the 22 PSU brackish water treated by the 2 mg/L initial 

TRO, even without dilution (refer to section 3.7, NIVA report). 

Two test waters with different qualities were adopted in the pilot tests carried in NIVA, 

according to the related Guidelines of IMO. Three different TRO levels were set in the tests, 

i.e. 1, 2 and 4 mg/L. After 5 days storage, toxicity tests of treated water were carried out for fish, 

invertebrate, and algae. Results show that the toxicity of treated seawater and brackish water is 

different. However, toxicity shows positive correlation with the TRO concentration, i.e. toxicity 

increases with the increase of TRO concentration, which indicates that toxicity is mainly caused 

by TRO. 

8 RISK ASSESSMENT 

8.1 Risks to the safety of the ship 

8.1.1 Corrosion 

All the units of this system, including the pipelines are made of anti-corrosion materials or in 

anti-corrosion coatings, and also ballast tanks have anti-corrosion coatings on themselves. In this 

system, organisms are killed by a certain concentration of oxidants. In the seawater itself, 

Cl–

poses corrosion to the ship. There is the possibility of enhancing the corrosion to ballast tank 

by the oxidants from this system. However, the degradation rate is very fast when the 

concentration of the oxidants is low, so the possibility of corrosion is predicted to be very low. 

Corrosion tests for this system will be carried out and data will be submitted in the application 

for Final Approval. 
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8.1.2 Fire and exposure 

In tests with 33 PSU seawater treated by 1 mg/L initial TRO and 22 PSU brackish water treated 

by 2 mg/L initial TRO, no hydrogen, chlorine, hydrogen sulfide, or surplus oxygen were 

detected. 

In the tests, on day 0, just after the treatment, 25 ppm carbon monoxide and 2.5% LEL 

(lower explosive limit) methane were detected. However, on day 5, these gases were not 

detected. 

Methane is flammable. When the concentration comes to 5%-15% in the air, it will cause fire. 

However, 2.5% LEL is far lower, so the possibility to cause fire is insignificant 

(refer to section 3.2, NIVA report) 

Carbon monoxide is toxic. The concentration threshold for workshop long-term exposure 

is 50 ppm. So exposure to 25 ppm carbon monoxide in short time will not pose toxicity to 

human. 

8.1.3 Storage, loading/unloading and noise 

The chemical substances are generated online in this system so there is no need to store, load or 

unload any chemical substances. 

When operating, there will be some noise from the fans of the system, and the effect on the 

surroundings and staff is insignificant. 

8.2 Risks to human health 

8.2.1 Human exposure scenario (HES) 

The document of assessment to human health risk will be submitted as an annex. There are 

Active Substances and Relative Chemicals generated by the system. When certain 

concentrations are reached, the substances will be harmful to human health. 

Since there is no data available on the toxicity to human, data on the experimental animals and 

the maximum allowable concentration to the environment determined by some relevant 

organizations are adopted as reference. The MOS values calculated from the measure-reaction 

relations, are all lower than the reference value MOSref, so the substances generated by the 

system can be acceptable to human body. Two groups, including the crew 

(occupational exposure) and people in public are tested and predicted in the human exposure 

scenario, on the different exposure approaches and exposure time. 

8.2.2 Risk control measures 

The possibility of leaking or breakdown of the system in normal working condition is 

insignificant, as the components used in the system are of good quality and stable performance. 

Once any error occurs, the system will be stopped working automatically instantly, and there will 

be light and sound alarms at the same time. When carrying out repairs, the staff should follow 

the existing safety protection measures on board. 
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8.3 Effects on the aquatic environment 

According to the analysis of test results above, after 5 days’ storage, in 33 PSU seawater treated 

by 1 mg/L initial TRO, and 22 PSU brackish water treated by 2 mg/L initial TRO, there are only 

a few Relevant Chemicals with very low concentrations, and the concentration 

of Active Substances detected is very low. Active Substances and Relevant Chemicals and the 

concentration are as follows (refer to sections 3.2, 3.4 and 3.5, NIVA report): 

Table 8.1 : Concentration of chemical substances, PEC and PNEC value 

(The highest concentration in the tested waters of different quality) 

Name Concentration PEC PNEC 

TRO (sodium 

hypochlorite) 

0.05 mg/L 0.0151μg/l 0.06μg/l 

Dibromochloromethane 1.7μg/l 3.2μg/l 

Tribromomethane 150μg/l 0.962μg/l 5.8μg/l 

Dibromoacetic acid 5.9μg/l 6.9μg/l 

2,4,6-tribromophenol 0.1μg/l 0.4μg/l 

Bromate ion 3.5μg/l 15.5μg/l 

Concentrations of dibromochloromethane, dibromoacetic acid, 2,4,6-tribromophenol and 

bromate ion, even in undiluted treated water, are lower than the PNEC value, so they will not 

have any effects on the aquatic environment when being discharged. Concentrations of 

tribromomethane and TRO in undiluted treated water exceed the relevant PNEC value, so treated 

water needs to be diluted in order to make sure it will not cause any effects to aquatics. By 

adopting the MAM-PEC model scenario, the PEC/PNEC value of tribromomethane and active 

chlorine calculated is lower than 1. Therefore, it is presumed that the possibility of toxicity from 

the treated ballast water to the environment is insignificant after dilution by port seawater. 

Results from toxicity testing of the treated ballast water is in line with what was expected from 

the PEC/PNEC assessment of Active Substances. Available data therefore do not indicate that 

there are Active Substances produced by the Ocean GuardTM, which are not already accounted 

for in the present assessment. 

Active Substances were also assessed for their Persistence-Bioaccumulation-Toxicity (PBT) 

potential. Although sodium hypochlorite shows significant chronic toxicity, no Active Substance 

fulfilled more than one of the PBT criteria, and therefore none are eligible for a PBT 

classification. 
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REFERENCES 

1. ATSDR, 2005. Toxicological Profile for Bromoform and Dibromochloromethane. 

2. Balster R.L, Borzelleca J.F., 1982. Behavioural Toxicity of Trihalomethane Contaminants 

of Drinking Water in Mice. Environ Health Perspect, 46: 127-136. 

3. Bouwer E.J., McCarty P.L., 1984. Modelling of Trace Organics Biotransformation in the 

Subsurface. Ground Water, 22:433-440. 

4. Bouwer E.J., Rittman B.E., McCarty P.L., 1981. Anaerobic Degradation of Halogenated 

l- and 2-Carbon Organic Compounds. Environ. Sci. Technol. 15:596-599. 

5. Bowman F.J., Borzelleca J.F., Munson A.E., 1978. The Toxicity of Some Halomethanes 

in Mice. Toxicol Appl Pharmacol, 44: 213-215. 

6. Boyle A.W., Phelps C.D., Young L.Y., 1999. Isolation from Estuarine Sediments of 

Desulfovibrio Strain Which Can Grow on Lactate Coupled to the Reductive Dehalogenation of, 

4,6-Tribromophenol. Environmental Microbiology, 65(3):1133-1140. 

7. Buccafusco R.J., Ells S.J., LeBlanc G.A., 1981. Acute Toxicity of Priority Pollutants to 

Bluegill (Lepomis macrochirus). Bull. Environ. Contam. Toxicol., 26(4): 446-452. 

8. Carbon monoxide OSHA. 

http://www.osha.gov/SLTC/healthguidelines/carbonmonoxide/recognition.html#healthhazard. 

9. Carlton B.D., Bartlett P., Basaran A., et al., 1986. Reproductive Effects of Alternative 

Disinfectants. Environ. Health Perspect., 69: 237-241. 

10. Chu I., Secours V.E., Marino I., et al., 1980. The Acute Toxicity of Four Trihalomethanes 

in Male and Female Rats. Toxicology and Applied Pharmacology, 52(2): 351-353. 

11. Church J.A., 1994. Kinetics of Uncatalysed and Cu (II)-catalysed Decomposition of 

Sodium Hypochlorite. Ind. Eng. Chem. Res., 33: 239-245. 

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