For reasons of economy, this document is pr inted in a limited number. Delegates are kindly asked to bring their copies to mee tings and not to request additional copies.

I:\MEPC\60\2-3.doc

INTERNATIONAL MARITIME ORGANIZATION



### IMO 

# E

MARINE ENVIRONMENT PROTECTION COMMITTEE 60th session Agenda item 2 MEPC 60/2/3 24 August 2009 Original: ENGLISH

HARMFUL AQUATIC ORGANISMS IN BALLAST WATER



### Application for Basic Approval of Sunrui ballast water management system

Submitted by China



### SUMMARY
Executive summary: This document contains non-confidential information for Basic Approval of Sunrui ballast water management system in accordance with the ìProcedure for approval of ballast water management systems that make use of Activ e Substances (G9)î adopted by resolution MEPC.169(57). The complete application dossier has been submitted to the Marine Environment Division of the IMO for review by the GESAMP-Ballast Water Wo rking Group in accordance with Procedure (G9).
Strategic direction: 7.1
High-level action: 7.1.2
Planned output: 7.1.2.4

Action to be taken: Paragraph 6

Related documents: BWM/CONF/36; MEPC 57/21; BWM.2/Circ.13 and BWM.2/Circ.18

Introduction

1 Regulation D-3.2 of the Inte rnational Convention for the Control and Management of Shipsí Ballast Water and Sediments stipulates th at ballast water management systems that make use of Active Substances to comply with the Convention shall be appr oved by the Organization.

2 The Procedure for approval of ballast water management systems that make use of Active Substances (G9) contains the information that should be included into a proposal for approval (MEPC 57/21, annex 1, paragraph 4.2.1) and provisions for risk characterization and analysis (MEPC 57/21, annex 1, paragraph 5.3). Accord ing to section 6 of Procedure (G9), the Organization should evaluate the info rmation provided in the application.

### MEPC 60/2/3 - 2 -

I:\MEPC\60\2-3.doc 

### 3 According to BWM.2/Circ.18, a document on th e proposal for approval containing all the non-confidential data related to the respective Active Substances shall be submitted to MEPC 60.

4 The competent authority in China has verifi ed the application dossi er and believes it satisfies the data requirements of Proce dure (G9) adopted by resolution MEPC.169(57).

5 China, therefore, submits the non-confidential part of the manu facturerís application dossier in the annex to this document to the Organiza tion for evaluation according to Procedure (G9). The complete dossier will be made available to the experts of the GESAMP-BWWG with the understanding of conf idential treatment.

Action requested of the Committee

6 The Committee is invited to consider th e proposal for approval and to decide as appropriate.

***

### MEPC 60/2/3

I:\MEPC\60\2-3.doc 

### ANNEX

NON-CONFIDENTIAL INFORMATIO N ON SUNRUI BALLAST WATER MANAGEMENT SYSTEM (CHINA)

This information related to the application for Basic Approval of Sunrui Ballast Water Management System is prepared in accordance with the Procedure for approval of ballast water management systems that make use of Ac tive Substances (G9) (MEPC.169(57)) and the Methodology for information gathering and the conduct of work of the GESAMP-BWWG (BWM.2/Circ.13).

1 INTRODUCTION

2 DESCRIPTION OF SUNRUI BALLAST WATER MANAGEMENT SYSTEM

2.1 Overview 2.2 Principle of chlorine disinfection 2.3 Sunrui BWMS configuration 2.4 Characteristics of Sunrui BWMS

3 IDENTIFICATION OF THE SUBST ANCE, RELEVANT CHEMICALS AND OTHER CHEMICALS (G9: 4.1)

3.1 Active Substance 3.2 Relevant Chemical 3.3 Other chemicals 3.4 Chemical analysis results

4 DATA-SET FOR ACTIVE SUBSTANC E AND PREPARATION (G9: 4.2)

4.1 Data on effects on aquatic plants, inverteb rates and fish, and other biota, including sensitive and representativ e organisms (G9: 4.2.1.1)

4.1.1 Acute aquatic toxicity 4.1.2 Chronic aquatic toxicity 4.1.3 Endocrine disruption 4.1.4 Sediment toxicity 4.1.5 Bioavailability/biomagnification/bioconcentration 4.1.6 Food web/population effects

4.2 Data on mammalian toxicity (G9: 4.2.1.2)

4.2.1 Acute mammalian toxicity 4.2.2 Effects on skin and eye, and sensitization effects 4.2.3 Repeated-dose toxicity 4.2.4 Chronic toxicity 4.2.5 Developmental and reproductive toxicity 4.2.6 Carcinogenicity 4.2.7 Mutagenicity/genotoxicity 4.2.8 Toxicokinetics

### MEPC 60/2/3 ANNEX Page 2

I:\MEPC\60\2-3.doc 

### 4.3 Data on e nvironmental fate and effect under aerobic and anaerobic conditions (G9: 4.2.1.3)

4.3.1 Modes of degradation (biotic; abiotic) 4.3.2 Bioaccumulation, partition coefficient, octanol/water partition coefficient 4.3.3 Persistence and identification of the ma in metabolites in the relevant media (ballast water, marine and fresh waters) 4.3.4 Reaction with organic matter 4.3.5 Potential physical effects on wildlife and benthic habitats 4.3.6 Potential residues in seafood 4.3.7 Any known inter active effects

4.4 Physical and chemical properties for the Active Substances, Relevant Chemicals and treated ballast water (G9: 4.2.1.4)

4.5 Analytical methods at environmentally relevant concentrations (G9: 4.2.1.5)

5 USE OF THE ACTIVE SUBSTANCE (G9: 4.2.6)

5.1 Manner of application 5.2 TRO dosage monitoring and control 5.3 Neutralizing unit and TRO monitoring at discharge 5.4 Retention time

6 MATERIAL SAFETY DAT A SHEETS (G9: 4.2.7)

7 RISK CHARACTERIZATION

7.1 Screening for persistence, bioaccumulation and toxicity (G9: 5.1)

7.1.1 PBT criteria for Active Substance (G9: 5.1.1.1) 7.1.2 Assessment of Persistence (P), Bioaccumulation (B) and toxicity (T) (G9: 5.1 .1.2)

7.2 Evaluation of the treate d ballast water (G9: 5.2)

7.2.1 Toxicity test of th e treated ballast water 7.2.2 Determination of holding time (G9: 5.2.7)

7.3 Risk characterization and analysis (G9: 5.3)

7.3.1 Reaction with organic matter (G9: 4.2.1.3) 7.3.2 Characterization of degrada tion route and rate (G9: 5.3.5) 7.3.3 Prediction of discharge and envir onmental concentrations (G9: 5.3.8) 7.3.4 Assessment of potential for bioaccumulation (G9: 5.3.7) 7.3.5 Effects assessment 7.3.6 Effects on aquatic organisms 7.3.7 Effects on sediment 7.3.8 Comparison of effect assessm ent with discharge toxicity

### MEPC 60/2/3 ANNEX

Page 3

I:\MEPC\60\2-3.doc 

### 8 RISK ASSESSMENT

8.1 Risk to safety of ship

8.1.1 Flooding 8.1.2 Corrosion 8.1.3 Fire and explosion 8.1.4 Hydrogen gas and chlorine gas 8.1.5 Storage and handling of the substances 8.1.6 Noise

8.2 Risks to human health 8.3 Risks to the aquatic environment

9 ASSESSMENT REPORT (G9: 4.3)

9.1 Test report and data quality

REFERENCES

### MEPC 60/2/3 ANNEX Page 4

I:\MEPC\60\2-3.doc 

### 1 INTRODUCTION

Sunrui Corrosion and Fouling Control Company (Sunrui CFCC) has developed a ballast water management system (Sunrui BWMS) to treat ballast water on board through pre-filtration followed by disinfection with Activ e Substances (AS) produced by an electrolytic process during ballasting, and neutraliza tion at de-ballasting.

When ballasting, the ballast wate r is firstly filtrated by an automatic self-cleaning filter with 50μm screen, to remove large plankton and solid particles. Then, at disinfection step, a side stream of seawater flows thr ough an electrolytic unit to produ ce sodium hypochlorite solution, which is injected back into the main ballast pipe to the ballast tanks to k ill the residual planktons, pathogens, larva or spores. Ballast water treate d by filtration and disinf ection steps fulfils the requirements contained in regula tion D-2 of the BWM Convention.

When de-ballasting, sodium thiosulfate solution is added into the treated ballast water to neutralize the residual TRO. The neutralization st ep will always be employed prior to discharge to ensure that no unacceptable risk is posed to the receiving environment. The dose of the neutralizing agent depends on the TRO concentration in the ballas t water for discharge and is controlled automatically.

Sunrui BWMS is developed on the basis of la nd-based electrolytic technology applied by Sunrui CFCC for many years, and the core technique is to electrolyse seawater onboard directly to produce sodium hypochlorite solution for steriliza tion. Sunrui CFCC owns the proprietary rights of core components, such as cell design, electrode material etc.

Sunrui CFCC has been engaged in the research and application of the seawater-electrolysis technique since the 1980s and has been the leadi ng enterprise in electr ochlorination industries in China. Its electrolysis technology has been used in coastal power plants (including nuclear power plants), chemical plants, desalinators, etc. The products of the company occupy more than 70% market share in seawater electrochlori nation field in China and so far Sunrui CFCC is the exclusive supplier in nuclear power plant field.

Sunrui CFCC started the development of BWMS in 2006. A prototype BWMS with treatment capacity of 250m 3 

### /h was designed and manufactured at the end of 2007.

In 2008, a land-based testing facility with flow rate of 250m 3 

### /h was established in Qingdao in accordance with Guidelines (G8). There are four simulated tanks in total, each with a volume of 250m 3 

### . Two tanks (Culture tanks) are used for preparing the inlet water to be tested. The other two tanks are used as holding tanks, one (Treat ed ballast tank) for storing treated water, and one (Control ballast tank) fo r keeping control water.

The performance tests of Sunrui BWMS menti oned in this document were conducted in the land-based set-up. Based on the testing and resear ch work, the basic operational parameters of the Sunrui BWMS have been defined. The initial biological efficacy tests indicate that ballast water treated by Sunrui BWMS can meet the D-2 standard criteria.

Meanwhile, the full dossier for the applicati on for the Basic Approval was prepared in accordance with Procedure (G9) and the GE SAMP-BWWG Methodology and is submitted to the GESAMP-BWWG for assessment.

### MEPC 60/2/3 ANNEX

Page 5

I:\MEPC\60\2-3.doc 

### Furthermore, an application for the Type Approva l of Sunrui BWMS has been submitted to the Chinese Administration. The land-based type appr oval testing is scheduled in July 2009 and the shipboard testing will be gin by the end of 2009. Tw o sets of Sunrui BWMS with rated capacity of 1,000 m 3 

### /h are under manufacturing for inst allation onboard ship this year.

2 DESCRIPTION OF SUNRUI BALLAST WATER MANAGEMENT SYSTEM

2.1 Overview Sunrui BWMS comprises:

.1 a filtration process using 50 μm filter; followed by;

.2 electrolysing seawater to pr oduce disinfection at intake; and

.3 a neutralization system to offset the residual TRO to the level below 0.1 ppm when de-ballasting.

The flow chart of treatment of Sunrui BWMS is shown in Figure 2-1.

Seawater is filtrated by a self-cleaning filter with 50 μ m, then a small amount of seawater is pumped into an electrolytic unit to generate sodium hypochlorite so lution, which is injected back into the main ballast stream after degasificatio n and makes a complete mixture with the main stream. The TRO level is measured by a TRO analyser and controlle d at a pre-set work concentration value (ranging from 8.0 to 9.5 pp m). The Sunrui electrochemical oxidation process employed a controlled cu rrent to ensure that the dos e of disinfectant produced is proportional with the ballast water uptake flow rate resulting in the pre-set level of TRO (8.0 to 9.5 ppm). The current is adjusted automatically through a rectifier acco rding to the signals from the TRO sensor, and then the TRO is produced in proportio n with the current to maintain the pre-set level. The flow char t of ballasting is shown in Figure 2-1 (a).

On discharge of the treated ballas t water, the Sunrui system monitors the levels of TRO in ballast water. Discharge does not start until the sensors are operational a nd the neutralizer feed system is functional. The neutralization system is activ ated with the neutralizer dose being calculated from the concentration of TRO measured just befo re the neutralizer injection point, to offset all the remaining TRO. The sodium thiosulfate soluti on is injected into the suction of the ballast pump by a metering pump. The other TRO sensor is installed after injec tion to monitor the TRO level to ensure that during discharge TRO con centration does not exceed 0.1 ppm at any time. The flow chart of de-ballasti ng is shown in Figure 2-1 (b).

### MEPC 60/2/3 ANNEX Page 6

I:\MEPC\60\2-3.doc 

### ( a ) Ballasting

( b ) De-ballasting

Figure 2-1: Flow chart of Sunrui BWMS

The Sunrui BWMS works in a c ondition where the ballast water is with a salinity of more than 3 PSU. In fresh water with a salt conten t below 3 PSU, salt will be needed to make the water achieve the minimum salinity of 3 PSU.

2.2 Principle of chlorine disinfection

Chlorination is a mature technique for water treatment and has been widely used for the sterilizations of potable wa ter, waste water and swimming pools for many years. The chlorination technique applied in Sunrui BWMS is to directly electrolyse seawater to produce the sodium hypochlorite solution in-situ . The principle of electrolysi ng seawater is: when a certain amount of seawater flows through the electrolytic cells, decompos ition reactions take place on the electrode surfaces, with chlorine produced at the anode and hydrogen gas at the cathode. The reaction mechanism is as follows:

### MEPC 60/2/3 ANNEX

Page 7

I:\MEPC\60\2-3.doc 

### Anode: 2Cl - 

### → Cl 2 

### + 2e

Cathode: 2H 2 

### O + 2e → 2OH - 

### + H 2 

### ↑

Chlorine gas can be dissolved in water to produ ce hypochlorous acid a nd hydrochloric acid rapidly:

Cl 2 

### + H 2 

### O → HOCl + Cl - 

### + H 

### So the overall reaction is:

NaCl + H 2 

### O → NaOCl + H 2 

### ↑

Hypochlorous acid is weak acid, which means that it tends to undergo partial dissociation as follows:

HOCl ⇋ H + 

### + OCl -



### to produce a hydrogen ion and a hypochlorite ion. In water of pH between 6.5 and 8.5 the reaction is incomplete and both species are present to some degree. The extent of this reaction can be calculated from the equation:

K

i 

### = HOCl OCl H ) )( (

− +



### where K i 

### is the ionization constant, varies in magn itude with temperature. The value of the constant ranges from 1.488x10 -8 

### mole/litre at 0 °C to 3.175 x10 -8 

### mole/litre at 30 °C

. Hypochlorous acid is the most germicidal of a ll chlorine compounds with the possible exception of chlorine dioxide. Undissociat ed HOCl species is a function of pH value and temperatures. The percentage of HOCl in diffe rent temperatures and pH valu es is shown in Table 2-1. The percentage of OCl - 

### is the difference between these numbers and 100.

### MEPC 60/2/3 ANNEX Page 8

I:\MEPC\60\2-3.doc 

### Table 2-1: The percent of HOCl in different temperature and pH value *



### pH 0 °C 5 °C 10 °C 15 °C 20 °C 25 °C 30 °C
5.0 99.85 99.82 99.80 99.79 99.74 99.71 99.68 5.5 99.53 99.45 99.36 99.27 99.18 99.09 99.00 6.0 98.53 98.28 98.00 97.73 97.45 97.18 96.92 6.1 98.16 97.84 97.50 97.16 96.82 96.48 96.15 6.2 97.69 97.29 96.88 96.45 96.02 95.60 95.20 6.3 97.11 96.62 96.10 95.57 95.05 94.53 94.04 6.4 96.39 95.78 95.14 94.49 93.84 93.21 92.61 6.5 95.50 94.75 93.96 93.16 92.37 91.60 90.87 6.6 94.40 93.47 92.51 91.54 90.58 89.65 88.78 6.7 93.05 91.92 90.75 89.58 88.43 87.32 86.27 6.8 91.41 90.03 88.63 87.23 85.85 84.54 83.31 6.9 89.42 87.77 86.10 84.43 82.82 81.29 79.86 7.0 87.04 85.08 83.10 81.16 79.29 77.53 75.90 7.1 84.22 81.92 79.63 77.39 75.26 73.27 71.44 7.2 80.91 78.25 75.64 73.11 70.73 68.52 66.52 7.3 77.10 74.08 71.15 68.35 65.75 63.36 61.22 7.4 72.78 69.42 66.20 63.18 60.39 57.87 55.63 7.5 67.99 64.33 60.88 57.68 54.77 52.18 49.90 7.6 62.79 58.89 55.27 51.98 49.03 46.43 44.17 7.7 57.27 53.23 49.54 46.23 43.32 40.77 38.59 7.8 51.57 47.48 43.81 40.58 37.77 35.35 33.30 7.9 45.82 41.79 38.25 35.17 32.53 30.28 28.39 8.0 40.18 36.32 32.98 30.12 27.69 25.65 23.95 8.1 34.79 31.18 28.10 25.50 23.32 21.51 20.01 8.2 29.77 26.46 23.69 21.38 19.46 17.88 16.58 8.3 25.19 22.23 19.78 17.76 16.10 14.74 13.63 8.4 21.10 18.50 16.38 14.64 13.23 12.07 11.14 8.5 17.52 15.28 13.46 11.99 10.80 9.84 9.06 8.6 14.44 12.53 11.00 9.77 8.77 7.97 7.33 8.7 11.82 10.22 8.94 7.92 7.10 6.44 5.91 8.8 9.62 8.29 7.23 6.39 5.72 5.18 4.75 8.9 7.80 6.70 5.83 5.15 4.60 4.16 3.81 9.0 6.29 5.39 4.69 4.13 3.69 3.33 3.05 9.5 2.08 1.77 1.53 1.34 1.19 1.08 0.98 10.0 0.67 0.57 0.49 0.43 0.38 0.34 0.31 10.5 0.21 0.18 0.15 0.14 0.12 0.11 0.10 11.0 0.07 0.06 0.05 0.04 0.04 0.03 0.03 11.5 0.02 0.02 0.015 0.013 0.012 0.01 0.01 11.7 0.01 0.01 0.01 0.01 0.007 0.007 0.006

Note : * From Page 189, Part 4 Chemistry of Chlorination, Ha ndbook of Chlorination and Alternative Disinfectants.



### Normally, natural seawater contains bromine ions with a density of 50~70 mg/L. The oxidation reaction between hypochlorous acid and brom ine ions will produce hypobromous acid:

HOCl + Br - 

### → HOBr + Cl -

### MEPC 60/2/3 ANNEX

Page 9

I:\MEPC\60\2-3.doc 

### Hypobromous acid will dissociate, as does hypochlorous acid depending upon pH, temperature and ionic strength as follows:

K = HOBr OBr H ) )( (

− +



### Where: K = 2 x 10 -9 

### at 20 °C

Hypobromous acid is also an effect ive biocide more stable than ch lorine under alkaline seawater. It is calculated that at pH 8, the undissociated HOBr is 83 percent vs. HOCl of only 28 percent.

In addition, the reaction of hypoc hlorous acid and hypobromous acid with ammonia in seawater generate chloramines (including monochloramine, dichloramine, trichloramine) and bromamines (including monobromamine, dibromamine, tribroma mine). The reaction equations for generating chloramines are as follows:

HOCl + NH 3 

### →

 NH 2 

### Cl ( monochloramine ) + H 2 

### O

NH 2 

### Cl + HOCl 

### →

 NHCl 2 

### ( dichloramine ) + H 2 

### O

NHCl 2 

### + HOCl 

### →

 NCl 3 

### ( trichloramine ) + H 2 

### O

Chloramines and bromamines are also germicidal agents, and it is generally considered that their bactericidal actions are much weaker than those of HClO/ClO 

### and HOBr/OBr - 

### . However, recent studies indicated that if chlora mines are allowed contact time of 45ñ60 minutes they are able to match the efficiency of free chlo rine based upon the destruction of coliform organisms.

In this document , the substances with bactericidal action mentioned above are HClO/ClO

- 

### /Cl 2 

### , HOBr/OBr - 

### /Br 2 

### , chloramines and bromamines, which are called by a joint name Total Residual Oxidants (TRO).

2.3 Sunrui BWMS configuration

Sunrui BWMS consists of th e following functional modules:

ñ Self-cleaning filter;

ñ Electrolytic unit (including electrolytic cells and accessory dosing and degassing units);

ñ Rectifier;

ñ Controller;

ñ TRO analyser;

ñ Neutralizing unit;

ñ Sampling unit; and

ñ Hydrogen gas/chlorine gas alarm.

### MEPC 60/2/3 ANNEX Page 10

I:\MEPC\60\2-3.doc 

### Accessory units include flow-meters, pumps, valv es, etc. Figure 2-2 s hows a typical Sunrui electrolytic unit.

Figure 2-2: Sunrui electrolytic unit

The functional modules of the system can be installed either as an integrated system in one space or installed separately in different places on the ship. The integrated BWMS is more suitable for new buildings, while different factional modules installed in different place may be more practicable for existing ships.

2.4 Characteristics of Sunrui BWMS

Sunrui BWMS has some special characteristics , in particular, in the following aspects:

Friendly to environment

No wastes like fume and dust that may po llute the environment are produced when the system operates. The substances produced by the system leave no harmful influences on natural environment.

Safe for ships and crew

The system does not produce any substances that do harm to the crew. All electrical and electronic sections that crew shall operate are safe. Adequate alarm system is designed, so that protective action could be taken in time to eliminate potential dangers for ships and crew.

Easy operation

The calibration and setting of the system ha ve been completed in the factory and the operation of the system can be performed in fully automatic mode. It is easy for operators to monitor the opera tional status of the system on the Human-Machine Interface (HMI) on the touch screen.

Low cost for operating and maintenance

For the operation of the system, only power consumption and a small amount of inexpensive reagent is needed.

### MEPC 60/2/3 ANNEX Page 11

I:\MEPC\60\2-3.doc 

### 3 IDENTIFICATION OF THE SUBST ANCE, RELEVANT CHEMICALS AND OTHER CHEMICALS (G9: 4.1)

3.1 Active Substance

Sunrui BWMS utilizes the tec hnology of electrolysing seawater di rectly to generate biocides in situ on board. In the disi nfection step, a side stre am of filtered seawat er (approximately 5.5 m 3 

### /h of 250 m 3 

### /h) flows through the electrolytic cells, in wh ich electrochemical react ions take place at the anode and cathode, with chlo rine and certain short-life oxyge nated chemical compounds and oxygen gas at the anode, and hydrogen gas generate d at the cathode. Chlorine dissolves into water and results in the formation of hypochlorou s acid (HOCl) in equilibrium with hypochlorite ion (OCl-); and a part of HOCl reacts with br omine ion in seawater and generates hypobromous acid (HOBr) in equilibrium w ith hypobromous ion (OBr-). Both HOCl/OCl- and HOBr/OBr- are effective biocides, usually called free availa ble halogen (FAH). The electrolysed water containing HOCl/OCl- and HOBr/OBr- is injected back into main ballast water stream by dosing pump to mix with ballast water.

Hydrogen gas and oxygen gas are completely removed in the degas tank, therefore they are considered as by-products and not Relevant Chemicals. The short-life oxygenated chemical species, possibly including hydrogen peroxide and ozone, present in the side-stream will decompose. For example, hydrogen peroxide will be reduced to water by free available chlorine and ozone will decompose into oxygen gas with chlo rine acting as a catalyst. Therefore, these oxygenated species will not be considered as eith er Active Substances or Relevant Chemicals.

Both HOCl and HOBr are strong oxidizers and ha logenation agents, which react with nitrogen compounds such as ammonia, urea, aminoacids, etc., present in fresh water or seawater, generating chloramines and/or bromamines, collec tively called haloamines. Both chloramines and bromamines are also biocides. Although the germicide efficiency of haloamines are much weaker than that of FAH, it be comes evident that those haloamines also have biocide effect, especially on certain pathogens , and have longer term effect.

Chlorine and bromine based compounds are typi cally analysed together and reported as Free Available Halogen (FAH) for total HOCl/O Cl- and HOBr/OBr- or as Total Residual Oxidant (TRO) for total HOCl/OCl-, HOBr/OBr-, ch loramines and bromamines. It is virtually impossible to provide a further breakdown for the concentration of chlora mines and bromamines in TRO, as these are unstable compounds and th ere are no calibration st andards available to ensure their reliable analysis.

Based on the above, for this application, HOCl/O Cl-, HOBr/OBr-, chloramines together with bromamines, regarded as TRO, ar e defined as Active Substances.

3.2 Relevant Chemical

During the process of disinfection by chlorine in seawater, trihalomethanes (THM), haloacetic acids (HAA), haloacetonitriles (HAN) and bromate ion are considered as main potential chemicals , therefore are defined as Relevant Chemicals.

3.3 Other chemical

On discharge of the treated balla st water, the TRO in ballast wa ter is neutralized with sodium thiosulphate, which is defined as other chemical.

### MEPC 60/2/3 ANNEX Page 12

I:\MEPC\60\2-3.doc 

### 3.4 Chemical analysis results

The potential by-products in the seaw ater treated by Surui BWMS have been tested and analysed. Based on the analysis results, the Active Substance, Relevant Chemicals and other chemicals identified are listed in Table 3-1. The chemical an alysis report is provided in appendix 2 of the confidential application dossier.

Table 3-1: Active Substances, Relevant Ch emicals and other ch emicals identified

Chemicals CAS No. Molecular weight Formula AS/ RC/ OC (bio)degradation rate or half-life

Hypochlorous acid /hypochlorite 7681-52-9 74.44 NaOCl AS 1.4 hour (at pH 8)

Hypobromous acid /hypobromite 13824-96-9 118.89 NaOBr AS Biodegrades fast

Chloramines/ Bromamines Not available 51.48 NH 2 Cl AS 9 to 420 hours (as Monochloramine)
Dibromochloromethane 124-48-1 208.28 CHBr 2 Cl RC Water: 38 days Soil: 75 days Sediment: 340 days Air: 280 days
Tribromomethane 75-25-2 252.73 CHBr 3 RC 1.7 years (Freshwater, at an aqueous concentration of 1X10 -17 mole/l hydroxyl radicals)
Monobromoacetic acid 79-08-3 167.01 CH 2 BrCOOH RC Half-life: Water: 8.7 days Soil: 17 days Sediment: 78 days Air: 22 days
Bromochloroacetic acid 5589-96-8 138. 95 CHBrClCOOH RC Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 24 days
Dibromoacetic acid 631-64-1 217.86 CHBr 2 COOH RC Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 25 days
Dibromochloroacetic acid 5278-95-5 252.36 CClBr 2 COOH RC No data available
Tribromoacetic acid 75-96-7 296.74 CBr 3 COOH RC Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 31 days

### MEPC 60/2/3 ANNEX Page 13

I:\MEPC\60\2-3.doc Chemicals CAS No. Molecular weight Formula AS/ RC/ OC (bio)degradation rate or half-life

Dibromoaceto-nitrile 3252-43-5 198.86 CHBr 2 CN RC Half-life: Water: 38 days Soil: 75 days Sediment: 340 days Air: 540 days
Bromate 7758-01-2 167.01 KBrO 3 RC Half-life: Seawater: 12 hours
Sodium thiosulfate 7772-98-7 158.09 Na 2 S 2 O 3 OC Biodegrades fast



### 4 DATA-SET FOR ACTIVE SUBSTANC E AND PREPARATION (G9: 4.2)

4.1 Data on effects on aquatic plants, invert ebrates and fish, and other biota, including sensitive and representative organisms (G9: 4.2.1.1)

4.1.1 Acute aquatic toxicity

Table 4-1: Acute aquatic toxicity

F
C Test Substance

A Species Test Type LC50/EC50 mg/L NOEC mg/L Reference/ Comments

Active Substances
Fresh
water Oncorhynchus gorbuscha 0.023- 0.052mg/L/96h ECB, IUCLID, 2000 F

Salt
water Oncorhynchus kisutch 0.032mg/L/ 96h (as TRO) ECB, IUCLID, 2000
Fresh
water Ceriodaphnia dubia 0.005mg/L/24h for HOCl(pH 7) Flowthrough tests (without food) Taylor, 1993 C

Salt
water B. plicatilis 0.01mg/L/ 30-60min The thermal stress Capuzzo, 1976, ECB, IUCLID, 2000 HOCl (NaOCl)

A Salt
water Thalassiosira guilardii EC50:0.075 mg/L/24h Gentile et al.
, 1976
F No data found in literature
C No data found in literature HOBr (NaOBr)

A No data found in literature

### MEPC 60/2/3 ANNEX Page 14

I:\MEPC\60\2-3.doc F
C Test Substance

A Species Test Type LC50/EC50 mg/L NOEC mg/L Reference/ Comments

F Notropis atherinoides (Emerald shiner) 0.63 mg/L 40 min exposures at 5 hr intervals for 24 hr, 10 °C ; 0.51 mg/L, 20 °C ; 0.35 mg/L, 30 °C HSDB, 2009

C Ceriodaphnia dubia (Water flea) 0.012 mg/L/ 24 hr Taylor PA, 1993 Chloramine

A No data found in literature
Relevant Chemicals
F Cyprinodon variegatus 7.1 mg/L/96hr Ward et al. , 1981

C Daphnia magna 46 mg/L/48 hr LeBlanc G.A, 1980Tribromomethane

A Skeletonema
costatum 12.3 mg/L/ 96hr(EC50) U.S. EPA 1978

F Cyprinus carpio 34 mg/L/72 to 120h Mattice et al.
, 1981 C N/A 27 mg/L/48h MEPC 58/2Dibromochloromethane

A Selenastrum caprocornutum 6.1 mg/L/72hr MEPC58/2

F No data found in literature
C Daphnia magna (Water flea) EC50 : 65 mg/L for 24 hr HSDB, 2009Monobromoacetic acid

A Scenedesmus subspicatus (Green algae, log growth phase) EC50 : 0.2 mg/L for 72 hr Kuehn R and Pattard M, 1990

F Pimephales promelas 6.9 mg/L/96 h Mayes et al. , 1985

C No data found in literature Dibromoacetic acid

A No data found in literature
F No data found in literature
C No data found in literatureTribromoacetic acid

A No data found in literature

### MEPC 60/2/3 ANNEX Page 15

I:\MEPC\60\2-3.doc F
C Test Substance

A Species Test Type LC50/EC50 mg/L NOEC mg/L Reference/ Comments

F No data found in literature
C No data found in literatureBromochloroacetic acid

A No data found in literature
F No data found in literature
C No data found in literatureDibromochloroacetic acid

A No data found in literature
F Pimephales promelas 0.55 mg/L/96 h Mayes MA et al.
, 1985
C Daphnia magna 3,897.8 mg/L/ 48hr ECOSARDibromoacetonitrile

A green algae 2,231.3 mg/L/96hr ECOSAR
F Morone Saxatilis 31 mg/L/96h Richardson et al., 1981
C Neomysis awatschnsis Opossum shrimp 176 mg/L/24h Crecelius, 1979 Bromate

A three seawater species EC50: 13.6 mg/L/72h Thomas H., 1997

Other chemicals
F Gambusia affinis (fresh water) Ca. 24000 mg/L/ 96hour ECB, IUCLID, 2000

C No data found in literature Sodium thiosulphate

A Ankistrodesmus falcatus Ca. 64 mg/L/ 1hour Wodzinski R.S. et al , 1978 

### F = Fish; C = Crustacean; A = Algae.

### MEPC 60/2/3 ANNEX Page 16

I:\MEPC\60\2-3.doc 

### 4.1.2 Chronic aquatic toxicity

Table 4-2: Chronic Aquatic Toxicity

F
C Test Substance

A Species Test Type LC50/ EC50 mg/L NOEC mg/L Reference Comments

Active Substances

Fresh
water Ictalurus punctatus NOEC: 0.005 mg/L/133day Hermanutz et al., 1990 F

Salt
water Menidia peninsulae NOEC: 0.04 mg CPO/lCPO = Chlorineproduced oxidants Goodman et al.
, 1983

C Pandalus danae (Salt-water) NOEC: 0.05 mg/L FREE Active Chlorine Gibson et al. , 1976 HOCl (NaOCl)

A algal biomass NOEC: 0.003 mg TRC/l Cairns, 1990

F No data found in literature
C No data found in literature HOBr (NaOBr)

A No data found in literature
F No data found in literature
C No data found in literature Chloramine

A No data found in literature

Relevant Ch e m ica l s F sheepshead minnows ( Cyprinodon variegatus ) NOEC: 4.8 mg/L/28d Ward et al. , 1981

C No data found in literatureTribromomethane

A Selenastrum Capricornutum NOEC: 10 mg/L/ 96h U.S. EPA 1978

F Oryzias latipes 3.2mg/L/21day IMO, MEPC 58/2
C No data found in literature Dibromochlor o-methane

A No data found in literature

### MEPC 60/2/3 ANNEX Page 17

I:\MEPC\60\2-3.doc F
C Test Substance

A Species Test Type LC50/ EC50 mg/L NOEC mg/L Reference Comments

F No data found in literature
C Daphnia magna NOEC: 1.6 (mg/L/21days) MEPC 58/2/7 GESAMP-BWWG 6/9, annex 7Monobromoacetic acid

A No data found in literature
F No data found in literature
C No data found in literature Dibromoacetic acid

A No data found in literature
F No data found in literature
C No data found in literatureTribromoacetic acid

A No data found in literature
F No data found in literature
C No data found in literatureBromochloroacetic acid

A No data found in literature
F No data found in literature
C No data found in literatureDibromochloroacetic acid

A No data found in literature
F No data found in literature
C No data found in literatureDibromoacetonitrile

A No data found in literature
F Morone Saxatilis LC50: (93) mg/L/10d, NOEC: (50) mg/L/10d Richardson et al.
, 1981

C No data found in literature Bromate

A Isochrysis galbana NOEC: 8 mg/L/7d Erickson and Freeman, 1978

### MEPC 60/2/3 ANNEX Page 18

I:\MEPC\60\2-3.doc F
C Test Substance

A Species Test Type LC50/ EC50 mg/L NOEC mg/L Reference Comments

Other chemicals

F Oncorhynchus mykiss 600mg/L/ 18 month In/with FW: NO MORTALITY, Temp:15°C pH: 7.82-7.92 ECB, IUCLID, 2000

C No data found in literature Sodium thiosulphate

A No data found in literature



### F = Fish; C = Crustacean; A = Algae.

4.1.3 Endocrine disruption

No reports were found, showing that the Active S ubstances might have any endocrine effects on aquatic organisms. Likewise, no reports were found, indicating the releva nt chemicals and other chemicals identified might have any e ndocrine effects on aquatic organisms.

4.1.4 Sediment toxicity

Table 4-3: Kocs for the Active Substances and Relevant Chemicals

Chemical Koc (L/kg) Reference Active Substances HOCl(NaOCl) 14.3 MEPC 58/2/7, GESAMP-BWWG 6/9, annex 6 HOBr(NaOBr) 14.3 MEPC 58/2/7, GESAMP-BWWG 6/9, annex 6 Chloramine Relevant Chemicals Tribromomethane 35.04 HSDB, 2009 Dibromochloromethane 95-468 MEPC 59/2/11 Monobromoacetic acid 39.8 HSDB, 2009 Dibromoacetic acid 1.5 HSDB, 2009 Tribromoacetic acid 5.3 HSDB, 2009 Bromochloroacetic acid 1.9 HSDB, 2009 Dibromochloroacetic acid Dibromoacetonitrile 13 HSDB, 2009 Bromate 2.7×10 -8 

### MEPC 58/2/7, GESAMP-BWWG 6/9, annex 5 Other Substances Sodium thiosulphate

### MEPC 60/2/3 ANNEX Page 19

I:\MEPC\60\2-3.doc 

### 4.1.5 Bioavailability/biomagnification/bioconcentration

Table 4-4: Log Pows and BCFs for the Active Substances and Relevant Chemicals

Chemical Log Pow BCF (L/kg) Reference Active Substances HOCl(NaOCl) -3.42 -2.19 MEPC 58/2/7, GESAMP-BWWG 6/9, annex 6 EPI SUIT (2007) HOBr(NaOBr) -1.03 1.24 MEPC 58/2/7, GESAMP-BWWG 6/9, annex 7 Chloramine Relevant Chemicals Tribromomethane 2.4 14 HSDB, 2009 Dibromochloromethane 2.24 0.74-1.47 MEPC 59/2/11 Monobromoacetic acid 0.41 3.2 HSDB, 2009 Dibromoacetic acid 0.70 0.17 HSDB, 2009

Tribromoacetic acid 1.71 0.63 HSDB, 2009

Bromochloroacetic acid 0.61 3.2 HSDB, 2009 Dibromochloroacetic acid 1.62 HSDB, 2009 Dibromoacetonitrile 0.47 3 HSDB, 2009 Bromate -7.18 3.7×10 -7 

### MEPC 58/2/7, GESAMP-BWWG 6/9, annex 5 Other chemicals Sodium thiosulphate -4.53 3.162 MEPC 58/2

4.1.6 Food web/population effects

Based on the low Kocs and Log Pows, little biomagnification and persistence in aquatic and mammalian food webs is anticipated from the Ac tive Substances, Relevant Chemicals and other chemicals. All of the Kocs for the Active Substances, Relevant Chemicals and other chemicals are <500 L/kg, which indicate that the chemicals would not readily be absorbed into sediments so that they would not be of concern to benthic populations and their food webs.

All the chemicals have established Bio-Concentrat ion Factors (BCFs). The BCFs show that little bioconcentration/bioaccumulation will occur in aquatic organisms. Little biomagnification occurs in aquatic food webs a nd bird/mammalian food webs since the chemicals are not readily bioconcentrated/bioaccumulated.

4.2 Data on mammalian toxicity (G9: 4.2.1.2)

The following tables summarize data on mamma lian toxicity for a variety of endpoints.

### MEPC 60/2/3 ANNEX Page 20

I:\MEPC\60\2-3.doc 

### 4.2.1 Acute mammalian toxicity

Table 4-5: Acute mammalian toxicity

Chemical Exposure Route Species Value Range Reference/Comments
a. Oral LD 50 (mg/L) b. Oral LD 50 (mg/L) a. Mouse b. Rat a. 880 mg/kg bw b. >5000 mg/kg bw ECB, IUCLID, 2000

Dermal LD 50 rabbit >10000 mg/kg bw ECB, IUCLID, 2000 HOCl(NaOCl)

Inhalation LC 50 (mg/L/4h) Rat >10.5mg/L/1h ECB, IUCLID, 2000

HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue.
Chloramine a. Oral LD 50 b. Oral LD 50 a. Rabbits: under 3 wk of age; older than 3 wk b. Rat a. LD:40-50 mg/kg; 60-70 mg/kg, respectively b. 935mg/kg a. HSDB, 2009 b. Mallinkrodt Baker, 2006

a. Oral LD 50 b. Oral LD 50 a. Male mice/female mice b. Male rats/ female rats a. 1,400 mg/kg/ 1,550 mg/kg b. 1388 mg/kg 1147 mg/kg a. Bowman, et al. , 1978 b. Chu, et al. , 1980Tribromomethane

Inhalation LC 50 a. Dog b. Mouse a. 7 mg/L/4 h b. 12.1mg/L/2h RTECS, 2006

Dibromochloromethane a. Oral LD 50 b. Oral LD 50 a. Male mice/female mice b. Male rats/ female rats a. 800 mg/kg/ 1,200 mg/kg b. 1186 mg/kg/ 848 mg/kg IPCS, 2000

Oral LD 50 Rat 50mg/kg RTECS, 2008
Dermal LD 50 Rabbit 59.9mg/kg RTECS, 2008Monobromoacetic acid

Inhalation LC 50 Rat Lowest published lethal concentration: 114 gm/m 3 /30 minute RTECS, 2008

Dibromoacetic acid Oral LD 50 Rat 1737 mg/kg Linder et al ., 1994

Tribromoacetic acid No data available; this compound is thought to be similar in toxicity to chlorinated analogue.
Bromochloroacetic acid No data found in literature

Dibromochloroacetic acid
Oral LD 50 Rat 245 mg/kg: male rats 361 mg/kg: female
rats Hayes JR et al. , 1986 Dibromo- acetonitrile

Inhalation LC 50 Rat 10g/m 3 /h IMO, MEPC 58/2

### MEPC 60/2/3 ANNEX Page 21

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Value Range Reference/Comments
Bromate a. Oral LD 50 b. Oral LD 50 a. Rat b. Mouse a. 157mg/kg b. 289mg/kg RTECS, 2007

Sodium thiosulphate a. Oral LD 50 b. Oral LD 50 a. Rat (males and females combined) b. Rat a. >5,050 mg/kg b. 2,500mg/kg to 5,000mg/kg a. EPA Federal Register Sodium thiosulfate, 2001 b. RTECS, 2006



### 4.2.2 Effects on skin and eye, and sensitization effects

Table 4-6: Skin, eye a nd sensitization effects

Chemical Skin Eye Sensitiz ation Reference/Comments HOCl(NaOCl) Irritation to the skin Irritation to the
eye 225 patients tested with sodium hypochlorite in patch test, 3 showed positive tractions (1.3%) ECB, IUCLID, 2000

HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue.
Chloramine Did not produce hyperplasia of the skin Irritation to the
eye Did not produce hyperplasia of the skin WHO, 2000 HSDB, 2009

Tribromomethane Irritation to the skin. Repeated or prolonged contact
may cause dermatitis Irritation to the eye. Repeated or prolonged contact may

cause dermatitis Skin : Y (Redness.) Inhalation : Y Reddening of the face. Salivation. Disturbance of
movements. Convulsions. Cough. Dizziness. Headache. HSDB, 2009 ICSC, 0108

Dibromochloro methane Irritation to the skin Irritation to the
eye Aldrich Chemical MSDS

Monobromoacetic acid Cause severe burns Cause severe burns HSDB, 2009

Dibromoacetic acid Cause burns Cause burns Inhalation may result in spasm, inflammation and edema of the larynx and bronchi, chemical pneumonitis, and pulmonary edema Sigma-Aldrich, 2006, MSDS

Tribromoacetic acid Irritating to the skin Irritating to the
eye Inhalation may result in spasm, inflammation and edema of the larynx and bronchi, chemical pneumonitis, and pulmonary edema Fisher Scientific MSDS HSDB, 2009

### MEPC 60/2/3 ANNEX Page 22

I:\MEPC\60\2-3.doc Chemical Skin Eye Sensitiz ation Reference/Comments
Bromochloroacetic acid Extremely destructive to shin Extremely destructive to
eye Sigma-Aldrich, MSDS 2006

Dibromochloroacetic acid Extremely destructive to shin Extremely destructive to
eye Inhalation may result in spasm, inflammation and edema of the larynx and bronchi, chemical pneumonitis, and pulmonary edema. Extremely destructive to tissue of the mucous membranes and upper respiratory tract. HSDB, 2009

Dibromoacetonitrile May cause skin irritation Cause eye irritation HSDB, 2009

Bromate May cause skin irritation Cause moderate eye irritation. May cause transient corneal injury. May cause skin irritation. May cause respiratory tract irritation. The Chemical Database

Sodium thiosulphate May cause skin irritation May cause eye irritation and possible burns May cause skin irritation. May cause respiratory tract irritation. The Chemical Database



### 4.2.3 Repeated-dose toxicity

Table 4-7: Repeated-d ose toxicity studies

Chemical Exposure Route Species Value Range Reference/ Comments HOCl(NaOCl) a. Oral, 13 weeks b. Oral, 90days a. F344 rats b. Mouse a. Significant suppression of body weight (as a result of decreased consumption of water and food) occurred at 0.2% and above. Slight damage to the liver as indicated by increased levels of serum enzymes (not specified) at 0.2% and 0.4% sodium hypochlorite in both sexes. No evidence of treatment-related pathology was observed in this study. b. NOAEL 50mg/L (10-12mg/kg/day) a. Hasegawa R, et al.
, 1986 b. Daniel, et al. , 1991

HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue.

### MEPC 60/2/3 ANNEX Page 23

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Value Range Reference/ Comments Chloramine a. Oral, 90-day(drinkingwater) b. Oral, 90-day(drinkingwater) a. SpragueDawley rats b. B6C3F1 mice a. NOAEL: 100mg/L, equivalent to 5.8 mg/kg bw/day. b. NOAEL: 50 mg/L, equivalent to 8.6 mg/kg bw/day. WHO, 2000

Tribromomethane a. Oral Gavage 5 days/week for 13 weeks b. Oral Gavage 5 days/week for 13 weeks a. F344/N rats/sex b. B6C3F1 mice a. LOAEL: 50 mg/kg/day (converted to 35.7 mg/kg/day) NOEL: 25 mg/kg/day (converted to 17.9 mg/kg/day) b. LOAEL: 50 mg/kg/day (converted to 35.7 mg/kg/day) NOEL: 25 mg/kg/day (converted to 17.9 mg/kg/day) NTP 1989

Dibromochloromethane a. Gavage, 13 weeks b. Gavage, 90 days a. Rats and mice b. Rats a. NOAEL:30 mg/kg-day b. Kidney damage at 50 and 100 mg/kg-day IPCS, 2000

Monobromoacetic acid Oral Pig Damage to the liver, heart, kidney, lung and skeletal muscle was found in pigs which died and movement disorders occurred in those that survived. HSDB, 2009

Dibromoacetic acid a. Oral, 28d b. Oral, 3 months a. Mouse b. Mouse a. NOAEL: 38 mg/kg/d b. No deaths but various effects seen at >500 mg/L WHO, 2004

Tribromoacetic acid No data found in literature
Bromochloroacetic acid a. Oral, 3 months b. Oral, 3 months a. B6C3F1 Mice b. F344/N Rats a. Mean body weight gains of females exposed to 250 mg/L or greater were significantly decreased. Liver weights of 1000 mg/L males and all exposed groups of females were significantly increased. All males and females exposed to 500 or 1000 mg/L had periportal cytoplasmic vacuolization. In the spleen, there were increased incidences of hematopoietic cell proliferation in 62.5, 125 and 250 mg/L males and 125 and 1000 mg/L females. HSDB, 2009

### MEPC 60/2/3 ANNEX Page 24

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Value Range Reference/ Comments b. Liver weights of 500 and 1000 mg/L males and females and kidney weights of 1000 mg/L males were significantly increased. In the liver, there were significantly increased incidences of cytoplasmic vacuolization in 10000 mg/L males and females.
Dibromochloroacetic acid No data found in literature

Dibromoacetonitrile Oral, 13 weeks SpragueDawley rats NOAEL: 10 ppm, equivalent to 1.11 and 1.21 mg/kg/day in the males and females, respectively Poon R et al. , 2003

Bromate Oral, 13 weeks Rats Liver toxicity at higher doses IPCS, 2000

Sodium thiosulphate No data found in literature



### 4.2.4 Chronic toxicity

Table 4-8: Chronic mammalian toxicity studies

Chemical Exposure Route Species Value Range Reference/ Comments HOCl(NaOCl) Oral, 2 years Rat and

mouse NOAEL: 14.4mg/kg/day NTP, 1992

HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue.
Chloramine Oral(drinkingwater) 2-year F344/N rats and B6C3F1 mice There was a decrease in mean bodyweight in high-dose rats. The highdose group had decreases in organweights and increases in organ-tobody weight ratios at 14- or 66- week evaluations. There was also a dose-related decrease in mean body weights of dosed male and female mice throughout the study. There were decreases in organ weights and increases in organ-to-body weight ratios observed in high-dose mice at 15- or 66-week evaluations. EPA, 1994

### MEPC 60/2/3 ANNEX Page 25

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Value Range Reference/ Comments
Tribromomethane a. Gavage 5 days/week for 2 years b. Gavage 5 days/week for 2 years a. F344/N
rats b. B6C3F1 mice a. NOAEL: 17.9 mg/kg/day b. NOAEL: 17.9 mg/kg/day NTP 1989

Dibromochloromethane Gavage, 2 years Mice and
rats Kidney and liver effects noted at all doses IPCS, 2000

Monobromoacetic acid No data found in literature
Dibromoacetic acid a. Oral, 2 years b. Oral, 2 years a. Mouse b. Rat a. Increased body weights at 50 and 500 mg/L in males only b. Decrease body weights at 500and 1000 mg/L NTP, 2007

Tribromoacetic acid No data found in literature
Bromochloroacetic acid a. Oral, 2 years b. Oral, 2 years a. B6C3F1 Mice b. F344/N Rats a. Survival of 1000 mg/L males was significantly less than that of the control group. Mean body weight of 1,000 mg/L males were 12% less than the control group after week 97, and those of 1,000 mg/L females were 8% less than the control group after week 21. b. Mean body weights of 500 mg/L males were 8% less than the control group after week 81, and those of 1000 mg/L males were 10% less than the control group after week 69. Mean body weights of 1000 mg/L females were 10% less than the control group after week 85. HSDB, 2009

Dibromochloroacetic acid No data found in literature
Dibromoacetonitrile Drinkingwater 2-year Mice and rat There was clear evidence ofcarcinogenic activity of dibromoacetonitrile in male rats based on increased incidences of squamous cell papillomas or carcinomas of the oral cavity; adenomas in the glandular stomach of male rats werealso considered to be exposurerelated. There was some evidenceof carcinogenic activity of dibromoacetonitrile in female rats based on an increased incidence of squamous cell papillomas of the oral cavity; increased incidences of basal cell or squamous cell neoplasms of the skin in female rats may have been related to dibromoacetonitrile NTP/NIEHS, 2008

### MEPC 60/2/3 ANNEX Page 26

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Value Range Reference/ Comments exposure. There was clear evidenceof carcinogenic activity of dibromoacetonitrile in male and female mice based on increased incidences of squamous cell papillomas or carcinomas of the forestomach. Increased incidences of neoplasms in the liver of male mice may have been related to dibromoacetonitrileexposure. Exposure to dibromoacetonitrile for 2 years caused increased incidences of epithelial hyperkeratosis in the esophagus of male and female rats, ectasia of the glandular stomach and squamous epithelial hyperplasia of the tongue in female rats, and squamous epithelial hyperplasia of the forestomach in male mice.
Bromate a. Drinkingwater, 100 weeksb. Drinkingwater, 100 weeks a. Male, B6C3F1 mice b. Male F344 rats a. NOAEL: 800mg/L b. NOAEL: 20mg/L WHO, 2005

Sodium thiosulphate No data found in literature



### 4.2.5 Developmental and repr oductive toxicity

Table 4-9: Developmental a nd reproductive toxicity

Chemical Exposure Route Species Effects Reference/ Comments HOCl(NaOCl) Oral Rat NOAEL: 14.4 mg/kg/day Druckrey, 1968 HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue.
Chloramine Gavage, 66-76 days Male (12/dose) and female (24/dose) Long-Evans
rats NOAEL:10 mg/kg/day Carlton et al. , 1986

### MEPC 60/2/3 ANNEX Page 27

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Effects Reference/ Comments
Tribromomethane a. Gavage, 105 days b. Gavage, days 6-15 a. Mice b. Rat a. No effect on fertility or offspring. b. An increased incidence of minor skeletal abnormalities, including appearance of a 14th rib, intraparietal deviations, and delayed ossification of sternebrae, was seen in developing foetuses at 100 and 200 mg/kg. a. WHO, EHC216 (2000) b. Ruddick, et al. 1983

Dibromochloromethane Exposed individually in 5 ml of embryo rearing solution, 15 days Medaka embryos at stage 10 (N= 60 per concentration) Embryos were evaluated daily for mortality and cardiovascular abnormalities. The heartbeat count was made for one full minute from day 3-10. The earliest lesion observed was the tubular heart on day 4 of exposure. Lack or incomplete chambers formation often began on day 5. Diathesis or pooling of blood in various tissues began to appear staring on day 5 of exposure, followed by slowing of blood flow and complete stasis usually on day 10. At this time pericardial edema began to develop and progressed to other organs and interfered with hatching which resulted in partial hatching. In addition, low incidence of the following lesions were observed: non-development of heart, absence or reduced numbers of vitelline vessels, reduced numbers of blood cells, and ruptured blood vessels. Palit S et al. (2004)

Monobromoacetic acid a. Oral intubation b. N/A a. Pregnant Long Evans
rats b. Rats a. These results suggest that bromoacetic acid is developmentally toxic at 100 mg/kg/day. b. Did not affect parameters related to male reproductive function a. Randall JL et al.
, 1991 b. Environmental Health Criteria 216

Dibromoacetic acid Oral Rat NOAEL:125 mg/kg/d Cummings et al ., 1998

Tribromoacetic acid Gavage Rat Tribromoacetic acid at up to 400 ppm marginally reduced water consumption and did not affect reproductive function or produce general toxicity. TBA is not a reproductive toxicant in males or females at doses up to 400 ppm. NTP, 1998

Bromochloroacetic acid Gavage SpragueDawley rats There were no clinical signs of general toxicity noted at any doselevel. There were no treatmentrelated effects on body weights or feed consumption. Water consumption was decreased NTP, 1998

### MEPC 60/2/3 ANNEX Page 28

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Effects Reference/ Comments by 21-34% at many of the intervals for the 600 ppm rats. The overall calculated consumption of BCA for Groups 2-4 was 7, 20, and 50 mg/kg/day, respectively. Clinical chemistry and hematology endpoints at necropsy were unaffected by BCA treatment except for a 16% increase in the albumin to globulin ratio in the 600 ppm A males; decreases of 15 and 20% in the alanine aminotransferase parameter in the 200 and 600 ppm A males, respectively; and increases of 5 and 9% in albumin in the 60 and 600 ppm A males, respectively. The increases in albumin to globulin ratio and albumin represent a small but possible biologically significant indicator of dehydration, probably attributable to decreased fluid consumption. The decreases in alanine aminotransferase are of little toxicological significance. Results of this study indicate that BCA at doses of 600 ppm produced a consistent decrease in water consumption in both sexes and affected reproductive function in females at a dose of 600 ppm. From these data, BCA is taste-aversive and a general toxicant in both sexes at 600 ppm and also a female reproductive toxicant at 600 ppm.
Dibromochloroacetic acid Drinkingwater rats The first range-finding study was conducted at concentrations of 0, 30, 100, 300, and 500 ppm of DBCA in the drinking-water for two weeks, with no significant test-article related effects observed at any dose level including 500 ppm. Following two weeks of a wash-out period, the second range-finding study was conducted at concentrations of 0, 750, 1000, and 1500 ppm of DBCA in the drinking-water for two weeks. During the treatment period, all animals survived to the scheduled necropsy. Body weights were 10-14% less than controls in the 1500 ppm A and C females. Water consumption was decreased at HSDB, 2009

### MEPC 60/2/3 ANNEX Page 29

I:\MEPC\60\2-3.doc Chemical Exposure Route Species Effects Reference/ Comments
several of the intervals for the 1000 and 1500 ppm dose groups. Water consumption was decreased by 12-49% at 1000 and 1500 ppm in both males and females throughout the course of the study. Results of this study indicate that DBCA at doses at and above 1000 ppm produced consistent decreases in food and water consumption in both sexes, but did not result in any female reproductive toxicity or any visceral malformation or variations in any pups. In the male reproductive data, a decrease of 11% in the male sperm velocity samples and in the male ALH max were observed in the 1500 ppm A male; no changes in fertility were noted.
Dibromoacetonitrile Gavage Long-Evans
rats Four of the 26 dams treated with dibromoacetonitrile died. There was a significant decrease in maternal weight gain during the period of treatment. Litter weight at the time of birth was lower than in the controls, and weight gain to lactation day 4 was significantly decreased. There was no significant effect on the percentages of pregnant females or resorptions and no effect on neonatal survival after birth. HSDB, 2009

Bromate Oral Rat NOAEL: 7.7 mg/kg/d NOEL: 22 mg/kg/d WHO, 2005

Sodium thiosulphate a. Oral b. Oral a. Mouse b. Rat a. There was no indication of any effect on maternal or foetal survival, or in incidences of visceral or skeletal abnormalities. b. There was no indication of any effect on maternal or foetal survival, or in incidences of visceral or skeletal abnormalities. EPA Federal Register Sodium thiosulfate, 2001.

### MEPC 60/2/3 ANNEX Page 30

I:\MEPC\60\2-3.doc 

### 4.2.6 Carcinogenicity

Table 4-10: Carcinogenicity

Chemical Carcinogen Classification Description Reference/ Comments HOCl(NaOCl) Not carcinogenic NTP, 1992 HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue. IARC Group 3 ñ not classifiable as to its carcinogenicity to humans. Inadequate evidence in humans and in experimental animals. IARC, 2004 Chloramine

Negative MOUSE, B6C3F1/male and female Oral, 0; 50; 100; 200 ppmin buffered, charcoalflltered, deionized water for 104 wk (study duration: 2 yr) CCRIS,1993

Tribromomethane IARC Group 3 ñ not classifiable as to carcinogenicity to humans WHO, EHC216 (2000)
Dibromochloromethane Group 3 ñ not classifiable as to its carcinogenicity IPCS, 2000

Monobromoacetic acid No data available

Dibromoacetic acid Carcinogenic (tumours/cancers observed) Mouse and rat NTP, 2007

Tribromoacetic acid No data available

Bromochloroacetic acid There was clear evidence of carcinogenic activity in male F344/N rats based on increased incidences of malignant mesotheliomas and adenomas of the large intestine. There was clear evidence of carcinogenic activity in female F344/N rats based on increased incidences of adenomas of the large intestine; increased incidences of multiple fibroadenomas of the mammary gland in female rats were also considered to be exposure related. Increased incidences of pancreatic islet adenomas in male rats and of hepatocellular adenomas in male and female rats may have been related to bromochloroacetic acid exposure. F344/N rats HSDB, 2009

### MEPC 60/2/3 ANNEX Page 31

I:\MEPC\60\2-3.doc Chemical Carcinogen Classification Description Reference/ Comments
Bromochloroacetic acid ( continued ) There was clear evidence of carcinogenic activity in male and female B6C3F1 mice based on increased incidences of hepatocellular neoplasms and hepatoblastoma (males only). Exposure to bromochloroacetic acid for 2 years resulted in increased incidences of nonneoplastic lesions in the liver of male rats, liver and lung of female rats, and liver of male and female mice. B6C3F1 mice HSDB, 2009

Dibromochloroacetic acid No data available

Dibromoacetonitrile Group 3-not classifiable as to its carcinogenicity to humans HSDB, 2009

Bromate IARC Group 2B- possibly carcinogenic to humans. Inadequate evidence in humans and sufficient evidence in experimental animals IPSC, 2000

Sodium thiosulphate No data available



### 4.2.7 Mutagenicity/genotoxicity

Table 4-11: Mutagenicity/genotoxicity

Chemical Study Results Reference/Comments HOCl(NaOCl) Mice Not mutagenic Hayashi, 1988 Meier et al. , 1985 HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue.
Chloramine Mice No evidence of any significant effects in any of the tests. USEPA, 1994

Salmonella tymphimurium in vitro. Positive Simmon et al. 1977; Simmon and Tardiff 1978 Salmonella tymphimurium in vitro

. Negative Rapson et al. 1980; Varma et al. 1988; Kubo et al. 2002 Human lymphocytes, in vitro. Increase in sister chromatid exchange Morimoto and Koizumi, 1983

Rat erythroblastic leukemia K3D, in vitro. Increase in sister chromatid exchange Fujie et al. , 1993 Tribromomethane

Chinese hamster ovary cells in vitro . No increase in sister chromatid exchange Galloway et al. , 1985

Dibromochloromethane Positive mutagenicity results in several in vitro and in vivo assays. IPCS, 2000

### MEPC 60/2/3 ANNEX Page 32

I:\MEPC\60\2-3.doc Chemical Study Results Reference/Comments
Monobromoacetic acid Salmonella typhimurium strains TA98, TA100, and RSJ100 +/- S9, Positive Kargalioglu Y et al. , 2002

Dibromoacetic acid Salmonella typhimurium, Ames test, Positive at 10 mg/L Giller et al. , 1997

Tribromoacetic acid Positive with metabolic activation in the Ames assay IPCS, 2000

Salmonella typhimurium strain TA100, in vitro, Positive in tests conducted with and without exogenous metabolic activation enzymes (S9) HSDB, 2009 Bromochloroacetic acid

Salmonella typhimurium strain TA98 or Escherichia coli WP2 uvrA/pKM101, in vitro, no mutagenicity was detected with or without S9 HSDB, 2009

Dibromochloroacetic acid No data available
Dibromoacetonitrile Rat intestinal epithelial cells, may trigger various forms of imbalance to intestinal mucosa and its functions USEPA. 2000

Bromate Weakly mutagenic in Ames assay with metabolic activation, caused chromosomal aberrations in Chinese hamster cell lines at high concentrations IPSC, 2000

Sodium thiosulphate Sodium thiosulfate was found to cause no mutagenic effects. EPA Federal Register Sodium thiosulfate, 2001.



### 4.2.8 Toxicokinetics

Table 4-12: Toxicokinetics

Chemical Study Results Reference/ Comments HOCl(NaOCl) Free chlorine is consumed upon contacting with living tissues, making measurement of biodegradation impossible and unnecessary. The chloride ion is actively transported by most freshwater and marine organisms, typically being concentrated in freshwater species and diluted in saltwater forms including some hyperosmotic and isotonic groups such as chondrichthys (sharks,rays etc). Free chlorine is very toxic to biodegrading microorganisms and may interfere with the biodegradation of other materials at levels of greater than or equal to 0.01 mg/L. ECB, IUCLID, 2000

HOBr(NaOBr) No data available; this compound is thought to be similar in toxicity to chlorinated analogue. Chloramine Information on the absorp tion of inorganic chloramines is extremely limited. In one study Abdel-Rahman et al. (1983) calculated an absorption rate constant for 36 Cl at 0.278 mg/hour (after 8 hours) with an absorption half-life of 2.5 hours after male Abdel-Rahman et al., 1983; Suh and Abdel-Rahman, 1983

### MEPC 60/2/3 ANNEX Page 33

I:\MEPC\60\2-3.doc Chemical Study Results Reference/ Comments Sprague-Dawley rats were administered a single oral dose of 4.6 mg/kg/day. After 48 hours the radiolabel was eliminated from the plasma with a half-life of 38.8 hours and a rate constant of 0.018 mg/hour. Absorption rates with respect to various dosage media and different routes of exposure were not available. The distribution of radiolabeled chlorine in the subfractions of rat liver homogenates, in organs, tissues and fluids was similar (120 hours) after oral administration of either 36Cl (200 mg/L as Na 36 Cl) or NH 2 36 Cl (370 mg/L NH 2 Cl). Plasma contained the highest concentrations of 36 Cl radioactivity for NH 36 Cl followed by whole blood skin, testes, packed cells, bone marrow, kidney, lung, stomach, thyroid, thymus, duodenum, spleen, carcass, liver, ileum and fat.
Tribromometha

ne The metabolism of bromoform, dibromochloromethane, and other trihalomethanes has been investigated by Anders and colleagues. The first step in th e metabolism of trihalomethanes is oxidation by the cytochrome P-450 mixed function oxidized system of liver. This has been demonstrated in vitro using isolated rat liver microsomes, and in vivo, where the rate of metabolism is increased by cytochrome P-450 inducers (phenobarbital) and decreased by cytochrome P-450 inhibitors (SKF-525A). The product of this reaction is presumed to be trihalomethanol, which then decomposes by loss of hydrogen and halide ions to yield the dihalocarbonyl. Although this intermediate has not been isolated , its formation has been inferred by the detection of 2-oxothiazolidine-4-carboxylic acid (OZT) in

an in vitro microsomal system metabolizing bromoform in the presence of cysteine. The dihalocarbonyl molecule (an analogue of phosgene) is highly reactive, and may undergo a number of reactions, including: (a) direct reaction with cellular nucleophiles to yield covalent adducts; (b) reaction with two moles of glutathione (GSH) to yield carbon monoxide and oxidized glutathione (GSSG); and (c) hydrolysis to yield CO2. The amount of trihalomethane metabolized by each of these pathways has not been studied in detail, but it appears that conversion to CO2 is the main route. However, this depends on the species, the trihalomethane being metaboli zed and metabolic conditions (cellular glutathione levels). Mink et al. (1986) found that mice oxidized 72% of an oral dose of dibromochloromethane and 40% of an oral dose of bromoform to CO2. In contrast, rats oxidized only 18% of dibromochlorometha ne and 4% of bromoform to CO2. The fraction of the dose converted to carbon monoxide has not been quantified, but dramati cally increased levels of carboxyhemoglobin have been reported follo wing oral exposure of rats to bromoform. Mink et al., (1986) reported that.about 10% of a dose of bromoform was present in blood in mice; the form of the label was not investigated, but it may have been carboxyhemoglobin. ATSDR, 2005

Dibromochloromethane Oral dosing in rats and mice showed that less than 2% of the dose was excreted in the urine in both species. Half-lives of DBCM in rats and mice were estimated to be 1.2 h and 2.5 h, respectively. IPCS, 2000

Monobromoacetic acid No data available

### MEPC 60/2/3 ANNEX Page 34

I:\MEPC\60\2-3.doc Chemical Study Results Reference/ Comments
Dibromoacetic acid Di-HAAs are nearly completely eliminated by metabolism and exhibit poor renal elimination. FPTC, 2006

Tribromoacetic acid Brominated tri-HAAs exhibit both moderate renal and metabolic elimination. FPTC, 2006

Bromochloroacetic acid Di-HAAs are nearly completely eliminated by metabolism and exhibit poor renal elimination. FPTC, 2006

Dibromochloroacetic acid No data available

Dibromoacetonitrile Urinary thiocyanate accounted for 2.25ñ12.8% of a single gavage dose of bromochloroacetonitrile, dibromoacetonitrile, dichloroacetonitrile or trichloroacetonitrile during the 24-h period following dosing of male rats. The cyanide carbon group is more readily excreted in the urine, whereas the halomethyl carbon group is excreted nearly equally in enhaled air and in urine; excretion in faeces is low. WHO, 2004

Bromate Bromate may be converted into hypobromic acid by hypochloric acid in the stomach. Liver and kidney tissues may degrade bromate to bromide by a process involving glutathione, although only a small amount appears to be reduced in this way. Bromate is excreted mainly by urine as bromate and bromide and some may also be eliminated by faeces. Bromate concentrationsin urine peak at about 1 hour, and bromate is not detectable in plasma after 2 hours4. MEPC 58/2/7, GESAMP-BWWG 6/9, annex 5

Sodium thiosulphate Sodium thiosulfate is poorly absorbed from bowel and thiosulfate ion distributes itself in extracellular fluid. HSDB, 2009



### 4.3 Data on environmental fate and eff ect under aerobic and anaerobic conditions (G9: 4.2.1.3)

4.3.1 Modes of degradation (biotic; abiotic)

The degradation information of the Active Substa nces, Relevant Chemicals and other chemicals are presented in Tables 4-13, 4-14 and 4-15. The resu lts show that the half-lives of the chemicals are ranging from hours to years. For example, the half-lives of HOCl are 0.8 hour (at pH 7) and 1.4 hour (at pH 8). Chloramine half-lives ar e ranging from 9 to 420 hours. Half-life of tribromomethane in freshw ater is 1.7 years and the half-lif e of monobromoacetic acid in water is 8.7 days, in soil: 17 days, in sediment: 78 days and in air: 22 days.

Table 4-13: Aerobic degradation for the Chemicals

Chemical Aerobic Degradation Reference/Comments HOCl(NaOCl) No data found HOBr(NaOBr) No data found
Chloramine No data found Tribromomethane 0% biodegradation in 4 weeks at 30 mg/L and the Japanese MITI test HSDB, 2009

Dibromochloromethane 25-39% loss in 28 days; HSDB, 2006

### MEPC 60/2/3 ANNEX Page 35

I:\MEPC\60\2-3.doc Chemical Aerobic Degradation Reference/Comments
Monobromoacetic acid Freshwater Mineralized in river water with 73% conversion to carbon dioxide in 8-10 days at 29oC. FPTC, 2006

Dibromoacetic acid Probability of Biodegradability =1.000/ Due to probability of biodegradability is greater than 0.7, dibromoacetic acid may be capable to biodegradation. MEPC 58/2

Tribromoacetic acid Probability of Rapid Biodegradation: Biowin 1(Linear model)-0.3565

Biowin 2(Non-linear model)-0.0000 Expert Survey Biodegradaion Results: Biowin3

(Ultimate surveymodel)- 2.7827 weeks Biowin4 (Primary survey model)- 3.7579 days MEPC 58/2

Bromochloroacetic acid Activated sludge
, 65% loss in 21 days Activated sludge
, 100% loss in 28 days ECB, IUCLID, 2000

Dibromochloroacetic acid Activated sludge
, 65% loss in 21 days Activated sludge
, 100% loss in 28 days ECB, IUCLID, 2000

Dibromoacetonitrile No data found
Bromate No data found Sodium thiosulphate No data found



### Table 4-14: Anaerobic degradation for the Chemicals

Chemical Anaerobic Degradation Reference/Comments HOCl(NaOCl) No data found HOBr(NaOBr) No data found
Chloramine No data found Approximately 20% of the initial concentration of 57 ug/L underwent biodegradation after 6.25 hours; approximately 30% biodegraded after 25 hours. Wookeun B et al. , 1990

Greater than 99% of the initia l concentration of 18 ug/L was removed under methanogenic, denitrification and sulfate reducing conditions after 2.5 days Bouwer EJ and Wright JP, 1988 Tribromomethane

Greater than 99% reducti on, initially present at 132-177 ug/L was observed after 1.5 hours Cobb GD and Bouwer EJ, 1991
Dibromochloromethane 100% loss in 2 weeks; mixed methanogenic bacterial culture HSDB, 2006

Monobromoacetic acid No data found
Dibromoacetic acid No data found
Tribromoacetic acid No data found
Bromochloroacetic acid Bacteria
, 100% loss in 2 days ECB, IUCLID, 2000
Dibromochloroacetic acid Bacteria
, 100% loss in 2 days ECB, IUCLID, 2000
Dibromoacetonitrile No data found
Bromate No data found Sodium thiosulphate No data found

### MEPC 60/2/3 ANNEX Page 36

I:\MEPC\60\2-3.doc 

### Table 4-15: The Half-lives of the Chemicals

Chemical Half-life Reference/Comments HOCl(NaOCl) Half-life:1.4 hour(at pH 8) Taylor, 1993 HOBr(NaOBr) Biodegrades fast MEPC 59/2/16 GESAMP-BWWG 8/6, annex 6 Chloramine Chloramine half-lives ranging from 9 to 420 hours HSDB, 2009

Tribromomethane Half-life (freshwater):1.7 years HSDB, 2009
Dibromochloromethane Half-life: Water: 38 days Soil: 75 days Sediment: 340 days Air: 280 days PBT Profiler

Monobromoacetic acid Half-life: Water: 8.7 days Soil: 17 days Sediment: 78 days Air: 22 days PBT Profiler

Dibromoacetic acid Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 25 days PBT Profiler

Tribromoacetic acid Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 31 days PBT Profiler

Bromochloroacetic acid Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 24 days PBT Profiler

Dibromochloroacetic acid No data found

Dibromoacetonitrile Half-life: Water: 38 days Soil: 75 days Sediment: 340 days Air: 540 days PBT Profiler

Bromate Seawater: 12 hours MEPC 57/2/10 GESAMP-BWWG 5/9, annex 5

Sodium thiosulphate Biodegrades fast MEPC 59/2/16 GESAMP-BWWG 8/6, annex 6



### 4.3.2 Bioaccumulation, partition coefficien t, octanol/water partition coefficient

The octanol/water partition coe fficients (Pows) and bioaccumul ation factors (BCFs) for the Active Substances
, Relevant Chemicals and other chemical s are given above in section 4.1.5. The adsorption coefficients (Kocs) for the Active Substances
, Relevant Chemicals and other chemicals are given in section 4.1.4.

### MEPC 60/2/3 ANNEX Page 37

I:\MEPC\60\2-3.doc 

### 4.3.3 Persistence and identification of th e main metabolites in the relevant media (ballast water, marine and fresh waters)

Active Substances have low Log Pow (range from -3.42 to -1.03) and BCF values and, therefore, it is expected they are not considered to be bi oaccumulation on aquatic organisms and to be main metabolites. For Relevant Chemicals and other chemicals, there is no food chain concentration potential. Due to low Log Pows and BCF values , it is unlikely that these will be accumulated through the aquatic organisms and metabolites.

4.3.4 Reaction with organic matter

It is well known that HOCl (NaOCl) reacts w ith organic matter in water forming by-products such as halomethanes and halogenated acetic acids.

For most of Relevant Chemicals, there is no accumulation through aquatic organisms and there is no available information on reaction with organic matter by Relevant Chemicals.

4.3.5 Potential physical effects on wildlife and benthic habitats

No data were found, indicati ng that the Active Substances
, Relevant Chemicals and other chemicals could cause potential physical effects to wildlife.

4.3.6 Potential residues in seafood

Based on the low log Pows and BCFs of the Activ e Substances, Relevant Chemicals and other chemicals, there is little possibi lity for significant residues to accumulate in tissues which could impact the consumption of seafood

4.3.7 Any known interactive effects

No interactive effects of the Active Substances , Relevant Chemicals an d other chemicals have been identified.

4.4 Physical and chemical properties for th e Active Substances, Relevant Chemicals and treated ballast water (G9: 4.2.1.4)

4.4.1 Physical and chemical prop erties for Active Substances

Hypochlorous acid/hypochlorite

Property Value Reference/Comments/ Justification for missing data Melting point (°C) - 20 to -30°C ECB, Risk Assessment Report for Sodium hypochlorite, 2007 Boiling point (°C) 96 ñ 120 °C ECB, Risk Assessment Report for Sodium hypochlorite, 2007 Flammability (flash point for liquids; °C) Non-flammable solution The Chemical Database

Density (20 °C; kg/m 3 ) 1.23 g/cm3 at 25°C ECB, Risk Assessment Report for Sodium hypochlorite, 2007

### MEPC 60/2/3 ANNEX Page 38

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Vapour pressure (20 °C; Pa) 17.4 - 20 hPa at 20°C ECB, Risk Assessment Report for Sodium hypochlorite, 2007 Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) Miscible [29.3 g/100 g (0 deg C) in water] ECB, Risk Assessment Report for Sodium hypochlorite, 2007 pH in solution >11@20°C Approx. 11 ECB, IUCLID, 2000

Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipmen t Contact with metals may evolve flammable hydrogen gas The Chemical Database

Reactivity to container material Contact with metals may evolve flammable hydrogen gas The Chemical Database

Auto-ignition temperature (°C) Non-fla mmable solution The Chemical Database Explosive properties Anhydrous sodium hypochlorite is very explosive. ECB, Risk Assessment Report for Sodium hypochlorite, 2007 Oxidizing properties Strong oxidizing agent usually stored and used in solution ECB, Risk Assessment Report for Sodium hypochlorite, 2007
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties N/A



### Hypobromous acid/hypobromite

Property Value Reference/Comments/ Justification for missing data Melting point (°C) -7.2 The Chemical Database Boiling point (°C) -58.7 The Chemical Database Flammability (flash point for liquids; °C) Non-flammability ICSC: 0107

Density (20 °C; kg/m 3 ) 3.121g/cm 3 The Chemical Database Vapour pressure (20 °C; Pa) 190mmHg (25°C) The Chemical Database Vapour density (air = 1) 5. 5 The Chemical Database
Water solu b ility (temp; effect of pH; mg/L) Insoluble The Chemical Database

pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipmen t Corrosiveness: Attacks all metals and organic tissues of plastics, only those which are fluorinated resist bromine attack. ECB, IUCLD, 2000

### MEPC 60/2/3 ANNEX Page 39

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Reactivity to container material Corrosiveness: Attacks all metals and organic tissues of plastics, only those which are fluorinated resist bromine attack. ECB, IUCLD, 2000

Auto-ignition temperature (°C) Flash point: -18°C The Chemical Database Explosive properties Not explosive ECB, IUCLD, 2000 Oxidizing properties A very powerful oxidizer ECB, IUCLD, 2000 Surface tension 40.9g/s 2 (25°C) The Chemical Database Viscosity 0.314sq mm/s The Chemical Database Thermal stability and identity of breakdown products Producing hydrogen bromide The Chemical Database

Other physical or chemical properties N/A



### Chloramine

Property Value Reference/Comments/ Justification for missing data Melting point (°C) -66 °C HSDB, 2009 Boiling point (°C) N/A Flammability (flash point for liquids; °C) N/A

Density (20 °C; kg/m 3 ) N/A Vapour pressure (20 °C; Pa) N/A Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) Soluble in water, alcohol and ether HSDB, 2009

pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products It may decompose violently above -66°C. When heated to decomposition it emits very toxic fumes of nitrogenoxides, ammonia, and hydrogen chloride. HSDB, 2009

Other physical or chemical properties Sensitive to light, temperature and pH change. Reacts with oxidizing materials. The Chemical Database

### MEPC 60/2/3 ANNEX Page 40

I:\MEPC\60\2-3.doc 

### 4.4.2 Physical and chemical propert ies for the Relevant Chemicals

Tribromomethane

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 9.2 The Chemical Database Boiling point (°C) 149.5 The Chemical Database Flammability (flash point for liquids; °C) 83 The Chemical Database

Density (20 °C; kg/m 3 ) 2.8912 g/cm 3 (20 C) The Chemical Database Vapour pressure (20 °C; Pa) 700 ICSC 0108 Vapour density (air = 1) 8. 7 The Chemical Database Water solubility (temp; effect of pH; mg/L) 0.1 g/100 g water at 20°C HSDB, 2009

pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipment Keep away from metals. Liquid bromoform will attack some forms of plastics, rubber, and coatings The Chemical Database HSDB, 2009

Reactivity to container material Do not store in metal containers Th e Chemical Database Autoignition temperature (°C) N/A Explosive properties N/A Oxidizing properties Strong oxidizing agents The Chemical Database Surface tension 41.53 dynes/cm at 20°C HSDB, 2009 Viscosity 1.73 cp (35 C) The Chemical Database Thermal stability and identity of breakdown products Stable at room temperature in closed containers under normal storage and handling conditions. Carbon monoxide, irritating and toxic fumes and gases, carbon dioxide, hydrogen bromide. The Chemical Database

Other physical or chemical properties Colourless liquid, with characteristic odour. Turns yellow exposure on light and air. ICSC 0108



### Dibromochloromethane

Property Value Reference/Comments/ Justification for missing data Melting point (°C) -20 °C HSDB, 2006 Boiling point (°C) 121.3-121.8°C HSDB, 2006 Flammability (flash point for liquids; °C) 20 °C The Chemical Database

Density (20 °C; kg/m 3 ) 2.38 HSDB, 2006 Vapour pressure (20 °C; Pa) 5.54 mm Hg at 25 deg C (est) HSDB, 2006

### MEPC 60/2/3 ANNEX Page 41

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Vapour density (air = 1) 7. 1 The Chemical Database Water solubility (temp; effect of pH; mg/L) 2.07×10 3 mg/L at 20°C HSDB, 2006

pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties Enthalpy of formation at 25°C: -5.0 kcal/mole (gas); Gibbs free energy of formation at 25°C: -4. 50 kcal/mole (gas); entropy at 25°C: 78.31 cal/mole (gas) HSDB, 2006



### Monobromoacetic acid

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 49 HSDB, 2009 Boiling point (°C) 208 HSDB, 2009 Flammability (flash point for liquids; °C) 113 Sigma-Aldrich, MSDS, 2006

Density (20 °C; kg/m 3 ) 1.9335 g/cm 3 The Chemical Database, 2009 Vapour pressure (20 °C; Pa) 0.09 mmHg (25°C) The Chemical Database, 2009 Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) Miscible The Chemical Database, 2009

pH in solution N/A Dissociation constant (pKa) 2. 72 The Chemical Database, 2009 Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A

### MEPC 60/2/3 ANNEX Page 42

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Surface tension 40.3 g/s 2 (55°C) The Chemical Database, 2009

Viscosity 3.65 cp (50°C) The Chemical Database, 2009

Thermal stability and identity of breakdown products Stable under normal temperatures and pressures. The Chemical Database, 2009

Other physical or chemical properties When heated to decomposition it emits toxic fumes HSDB, 2009



### Dibromoacetic acid

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 48°C HSDB, 2009 Boiling point (°C) 232-234°C HSDB, 2009 Flammability (flash point for liquids; °C) 94°C The Chemical Data base Density (20 °C; kg/m 3 ) N/A Vapour pressure (25 °C; Pa) 2.3×10-2 mm Hg HSDB, 2009 Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) Very soluble The Chemical Database pH in solution N/A Dissociation constant (pKa) 1.47( pKa) The Chemical Database Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties N/A



### Tribromoacetic acid

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 135°C Th e Chemical Database Boiling point (°C) 245°C The Chemical Database Flammability (flash point for liquids; °C) N/A Density (20 °C; kg/m 3 ) N/A Vapour pressure (20 °C; Pa) 0.00028mmHg at25°C HSDB, 2009

### MEPC 60/2/3 ANNEX Page 43

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) 20000mg/L HSDB, 2009 pH in solution N/A Dissociation constant (pKa) 0.72 at 25°C HSDB, 2009 Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties N/A



### Bromochloroacetic acid

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 38 The Chemical Database Boiling point (°C) 201 The Chemical Database Flammability (flash point for liquids; °C) 110 Sigma-Aldrich, MSDS 2006 Density (20 °C; kg/m 3 ) 1.9848 g/cm 3 (31 °C) HSDB, 2009 Vapour pressure (20 °C; Pa) 1.4×10 -1 mmHg at 25 °C HSDB, 2009 Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) 2.5×10 +5 mg/L at 25 deg C HSDB, 2009 pH in solution N/A Dissociation constant (pKa) 1.40 HSDB, 2009 Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties Henryís Law constant = 2.2×10-8 atm-cu m/mole at 25 deg C HSDB, 2009

### MEPC 60/2/3 ANNEX Page 44

I:\MEPC\60\2-3.doc 

### Dibromochloroacetic acid

Property Value Reference/Comments/ Justification for missing data Melting point (°C) N/A Boiling point (°C) N/A Flammability (flash point for liquids; °C) N/A Density (20 °C; kg/m 3 ) N/A Vapour pressure (20 °C; Pa) 5.2×10 -3 mm Hg at 25 C (est) HSDB, 2009 Vapour density (air = 1) Water solubility (temp; effect of pH; mg/L) In water, 2.4×10 3 mg/L at 25°C HSDB, 2009

pH in solution N/A Dissociation constant (pKa) 0.03 HSDB, 2009 Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties Henryís Law constant = 2.6×10 -9 atm-cu m/mole at 25°C HSDB, 2009



### Dibromoacetonitrile

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 6.98°C MEPC 58/2 Boiling point (°C) 67°C The Chemical Database Flammability (flash point for liquids; °C) Non -flammability (37°C) The Chemical Database Density (20 °C; kg/m 3 ) 2.369 g/cm 3 (20°C) The Chemical Database Vapour pressure (20 °C; Pa) 2mmHg The Chemical Database Vapour density (air = 1) 6. 86 The Chemical Database Water solubility (temp; effect of pH; mg/L ) Slightly soluble The Chemical Database pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A

### MEPC 60/2/3 ANNEX Page 45

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Explosive properties N/A Oxidizing properties N/A
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties N/A



### Bromate

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 350 The Chemical Database Boiling point (°C) Decomposition poin t: 370°C The Chemical Database Flammability (flash point for liquids; °C) N/A Density (20 °C; kg/m 3 ) 3.218 g/cm 3 The Chemical Database Vapour pressure (20 °C; Pa) N/A Vapour density (air = 1) 5.8 Water solubility (temp; effect of pH; mg/L) 75 g/L pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties N/A Oxidizing properties Oxidizer The Chemical Database
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products N/A

Other physical or chemical properties N/A



### 4.4.3 Physical and chemical prop erties for the Other Chemicals

Sodium thiosulphate

Property Value Reference/Comments/ Justification for missing data Melting point (°C) 48 The Chemical Database Boiling point (°C) 100 The Chemical Database Flammability (flash point for liquids; °C) Non-flammable ECB, IUCLID, 2000 Density (20 °C; kg/m 3 ) 1740 kg/m 3 ECB, IUCLID, 2000

### MEPC 60/2/3 ANNEX Page 46

I:\MEPC\60\2-3.doc Property Value Reference/Comments/ Justification for missing data Vapour pressure (20 °C; Pa) N/A Vapour density (air = 1) N/A Water solubility (temp; effect of pH; mg/L) 701g/l at 20 °C pH: Ca. 6.5-9 at 100g/l and 25°C ECB, IUCLID, 2000

pH in solution N/A Dissociation constant (pKa) N/A Oxidation-reduction potential N/A Corrosivity to material or equipment N/A Reactivity to container material N/A Auto-ignition temperature (°C) N/A Explosive properties Not explosive ECB, IUCLID, 2000 Oxidizing properties No oxidizing properties ECB, IUCLID, 2000
Surface tension N/A Viscosity N/A Thermal stability and identity of breakdown products Stable under normal temperatures and pressures. Decomposition: Oxides of sulfur, hydrogen sulfide, sodium oxide. ECB, IUCLID, 2000

Other physical or chemical properties N/A



### 4.4.4 Physical and chemical properties of the treated and untreated seawater

Property Untreated seawater Treated seawater Melting point (°C) N/A N/A Boiling point (°C) N/A N/A Flammability (flash point for liquids; °C) N/A N/A Density (20 °C; kg/m 3 ) 1.0235 1.0235 Vapour pressure (20 °C; Pa) N/A N/A Vapour density (air = 1) N/A N/A Water solubility (temp; effect of pH; mg/L) N/A N/A pH in solution 8.23 8.09 Dissociation constant (pKa) N/A N/A Oxidation-reduction potential 283 287 Corrosivity to material or equipment / / Reactivity to container material N/A N/A Auto-ignition temperature (°C) N/A N/A Explosive properties N/A N/A Oxidizing properties N/A N/A
Surface tension N/A N/A Viscosity N/A N/A

### MEPC 60/2/3 ANNEX Page 47

I:\MEPC\60\2-3.doc Property Untreated seawater Treated seawater Thermal stability and identity of breakdown products N/A N/A

Salinity 30.13 29.74 TOC , % particulate matter 1.90 3.21 DOC , % particulate matter 1.75 2.89 Other physical or chemical properties N/A N/A



### 4.5 Analytical methods at environmentally relevant concentrations (G9: 4.2.1.5)

Analytical methods at environmentally releva nt concentrations are shown in Table 4-16.

Table 4-16: Analytical me thods at environmentally relevant concentrations

Chemicals Methods Haloalkanes EPA524.2 Haloacetic acids EPA552.3 Haloacetonitriles EPA551.1

HOCl(ClO - ) Chloramines and Bromamines EPA330.5, GB/T 5750.11-2006, 4500-Cl G. (Standard Methods for the Examination of Water and Wastewater, 21st Edition) HOBr(BrO - ) PONY-BJXZSZ037-2009A Sodium thiosulphate PONY-BJXZSZ038-2009A Bromate ion EPA317.0



### 5 USE OF THE ACTIVE SUBSTANCE OR PREPARATION (G9: 4.2.6)

5.1 Manner of application

For Sunrui BWMS, filtration process does not pr oduce or involve any Active Substance. In disinfection process, the Sunrui BWMS utilizes the technology of electrolysing seawater directly to generate biocides in-situ onboard. As reported in Section 2, a side str eam of filtered seawater flows through the electrolytic cells, in which elect rochemical reactions take place to generate Active Substances, including HClO/ClO

- , HOBr/OBr-, chloramines and bromamines, which are called by a joint name Total Residual Oxidants (TRO). After degas, the TRO solution is injected back into the main ballast pipe and mi xed with incoming ballast water in the pipe. The initial TRO concentration value in the treated ball ast water is pre-set in the system, and the dose range in the Sunrui BWMS is between 8.0 and 9.5 ppm.

During electrolysis, hydrogen gas is produced, which is a hazard to safety of ships. In the system, hydrogen gas is fully separated and diluted in a de gas unit, and then discharged to atmosphere outside ships. Risk management measures in th is regard are described in detail in Section 10.1.

5.2 TRO dosage monitoring and control

In TRO dosage control system, the controlling prin ciple is based on maintaining TRO levels in the treated ballast water at the set value. A TRO analyser is incorporated in the BWMS to control the TRO concentration on line th rough measuring the actual TRO c oncentration in the treated ballast water, flow and electri c conductivity, which has direct relation with the TRO production.

### MEPC 60/2/3 ANNEX Page 48

I:\MEPC\60\2-3.doc 

### During treatment process, the actual TRO concentr ation in the treated ballast water is measured and compared with the pre-set conc entration value of TRO, and then the current will be regulated automatically through a rectifier to adjust th e TRO production so as to maintain the TRO concentration at the set value.

5.3 Neutralizing unit and TRO monitoring at discharge

When de-ballasting, sodium thiosulfate solution is added into the treated ballast water to neutralize the residual TRO. The chemical reaction equation is as follows:

Na 2 

### S 2 

### O 3 

### + 4NaCl O + 2NaOH → 4NaCl + 2Na 2 

### SO 4 

### + H 2 

### O

NaCl and Na 2 

### SO 4 

### produced in the neutralization reaction are the substances already existing in seawater, so they will not cause a ny risk to the marine environment.

The neutralization step will be always employed pr ior to discharge to ensure the safety of the marine environment in receiving water. The do se of the neutralizing agent depends on the TRO concentration in the ballast water for discharge and ballast water flow rate, and is controlled automatically.

In neutralization process, filter and electrolytic unit are bypassed. On discharge of the treated ballast water, the TRO analyser monitors the leve ls of TRO in ballast water. Discharge does not start until the TRO analyser is operational and th e neutralizer feed system is functional. The neutralization system is activated with the neutralizer dose being calculated from the concentration of TRO measured just before the neutralizer injection point, to offset all remaining TRO. The sodium thiosulfate solution is injected into the suction side of the ballast pump by a metering pump. The TRO analyser is also used to monitor the TRO level after injection to ensure that during discharge TRO concentr ation does not exceed 0.1 ppm at any time.

If the TRO concentration exceeds 0.1 ppm, an audi ble and visual alarm will be triggered and the discharge will stop. Instructions on how to carry out the inspection and take remedy actions will be shown on HMI.

5.4 Retention time

Retention time in the Sunrui BWM system was dete rmined based on the biologi cal efficacy tests. According to the test results, 24 hours of stori ng of ballast water in the ballast tanks after treatment can ensure effective disinfection, which meets regu lation D-2 and no re-growth of organisms were found in the treated water after 5 days.

In conclusion, in order to meet regulation D-2, th e treated ballast water s hould be kept in ballast tanks for 24 hours befo re de-ballasting.

6 MATERIAL SAFETY DAT A SHEETS (G9: 4.2.7)

Material Safety Data Sheets (MSDS) for Acti ve Substances, Relevant Chemicals and other chemical are provided in appendix 6 of the confiden tial application dossier.

### MEPC 60/2/3 ANNEX Page 49

I:\MEPC\60\2-3.doc 

### 7 RISK CHARACTERIZATION

7.1 Screening for persistence, bioaccumu lation and toxicity (G9: 5.1)

7.1.1 PBT criteria for Active Substance (G9: Table 1)

Table 7-1 shows the criteria for identification of PBT substances.

Table 7-1: Criteria for identi fication of PBT substances

Criterion PBT criteria
Persistence Half-life: > 60 days in marine water, or > 40 days in freshwater, or > 180 days in marine sediment, or > 120 days in freshwater sediment Bioaccumulation BCF > 2,000 or LogPoctanol/water ≥ 3 Toxicity Chronic NOEC < 0.01 mg/L

7.1.2 Assessment of Persistence (P), Bi oaccumulation (B), and Toxicity (T)

Table 7-2 shows Persistence (P), bioaccumulati on (B), and toxicity (T) data for the Active Substances, Relevant Chemicals and other chemi cals. According to PBT evaluation, all of the Active Substances, Relevant Chemicals and ot her chemicals are not considered to be PBT substances.

Table 7-2: Persistence (P), bioaccumulation (B), and toxicity (T) data for the Active Substances, Relevant Chemicals and other chemicals

Chemical Persistence (Y/N) Bioaccumulation (Y/N) Toxicity (Y/N) HOCl(NaClO) No Half-life: 1.4 hour (at pH 8) No BCF: -2.19 Log Pow: -3.42 Yes NOEC: 0.005 mg/L/134 day

HOBr(NaBrO) No Biodegrades fast No BCF: 1.24 Log Pow: -1.03 N/A

Monochloramine No Abiotic Degradation: Chloramine half-lives ranging from 9 to 420 hours N/A. N/A

### MEPC 60/2/3 ANNEX Page 50

I:\MEPC\60\2-3.doc Chemical Persistence (Y/N) Bioaccumulation (Y/N) Toxicity (Y/N)
Tribromomethane Yes Fresh water, Half-life: 1.7 years (at an aqueous concentration of 1X10 -17 mole/l hydroxyl radicals) No BCF: 14 Log Pow: 2.4 No NOEC: 4.8 mg/L/28d

Dibromochloromethane Yes Half-life: Water: 38 days Soil: 75 days Sediment: 340 days Air: 280 days No BCF: 0.74-1.47 L/kg Log Pow: 2.24 No NOEC: 3.2mg/L/21day

Bromoacetic acid No Half-life: Water: 8.7 days Soil: 17 days Sediment: 78 days Air: 22 days No BCF: 3.2 Log Pow: 0.41 No NOEC: 1.6 mg/L/21days

Dibromoacetic acid No Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 25 days No BCF: 0.17 Log Pow: 0.70 No PBT Profiler

Tribromoacetic acid No Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 31 days No BCF: 0.63 Log Pow: 1.71 No PBT Profiler

Bromochloroacetic acid No Half-life: Water: 15 days Soil: 30 days Sediment: 140 days Air: 24 days No BCF: 3.2 Log Pow: 0.61 No PBT Profiler

Dibromochloroacetic acid No Activated sludge: 100%(aerobic), 28 days No Log Pow: 1.62 N/A.

Dibromoacetonitrile No Half-life: Water: 38 days Soil: 75 days Sediment: 340 days Air: 540 days No BCF: 3 Log Pow: 0.47 No PBT Profiler

Bromate No Half-life: Seawater: 12 hours No BCF: 3.7×10 -7 Log Pow: -7.18 No NOEC: 8 mg/L/7d

Sodium thiosulfate No Biodegrades fast No BCF: 3.162 Log Pow: -4.53 No NOEC: 600mg/L/18month

### MEPC 60/2/3 ANNEX Page 51

I:\MEPC\60\2-3.doc 

### 7.2 Evaluation of the treated ballast water (G9: 5.2)

7.2.1 Toxicity test of th e treated ballast water

According to the requirements of the ìProcedur e for approval of ballast water management systems that make use of Active Substances (G9)î and the Methodology for information gathering and conduct of work of the GESA MP-BWWG (the Methodology) (BWM.2/Circ.13), the aquatic toxicity tests of three trophic levels for ballast water treated by Qingdao Sunrui ballast water management system have been performed by Supervision and Test Center for Pesticide Safety Evaluation and Quality Control.

Algae Growth inhibition Test

A growth inhibition test of ballast wate r treated by Sunrui BWMS was conducted to Skeletonema
costatum . The definitive test was conducted with the 100% ballast water treated by Sunrui BWMS under the laboratory conditions. During the 96-hour test period, growth inhibition and other toxic signs were not observed in treated and c ontrol cultures. The test results indicated that I r 

### C 50 

### (96hr), I y 

### C 50 

### (96hr) and NOAEC (No Observed A dverse Effect Concentrations) to Skeletonema costatum were all greater than 100% ballas t water treated by Sunrui BWMS.

Marine Invertebrate Acute Toxicity Test

An acute toxicity test of ballast wate r treated by Sunrui BWMS was conducted to Neomysis awatschensis . The definitive test was conducted with the 100% ballast water treated by Sunrui BWMS under the laboratory conditions. During the 96-hour exposure period, mortalities of the test organisms in treated and control water were all less than 10 percent. The test results indicated that LC 50 

### (96h) and NOAEC (No Observed Adve rse Effect Concentration) to Neomysis awatschensis were all greater than 100% ball ast water treated by Sunrui BWMS.

Marine Invertebrate Chronic Toxicity Test

Based on the result of acute toxicity test and requirements of relevant guidelines, the definitive test was conducted with the 6.25%, 12.5%, 25%, 50% , and 100% ballast water treated by Sunrui BWMS under the laboratory conditi ons. A chronic toxicity test of ballast water treated by Sunrui BWMS was conducted to Neomysis awatschensis . During the 7-day test period, mortalities of the test organisms in treated and control were all less than 10 percent. Te st results indicated no chronic toxicity to survival and growth in Neomysis awatschensis at any test concentrations. IC 25 

### (7d), NOEC and LOEC to Neomysis awatschensis were all greater than 100% ballast water treated by Sunrui BWMS.

Marine Fish Acute Toxicity Test

An acute toxicity study of ba llast water treated by Sunrui BWMS was conducted to Bareneck goby (Ctenogobius gymnauchen). The definitive test was conduc ted with 100% ballast water treated by Sunrui BWMS under the laboratory c onditions. During the 96-hours test period, the fish treated with the 100% ballast water treate d by Sunrui BWMS showed no visibly toxic signs or mortality during the test period. The test resu lts indicated that ìmedian lethal concentrations (LC 50 

### )î and ìno observed advers e effect concentrations (NOAEC)î to Bareneck goby (Ctenogobius gymnauchen) were greater than 100% ballas t water treated by Sunrui BWMS.

### MEPC 60/2/3 ANNEX Page 52

I:\MEPC\60\2-3.doc 

### Marine Fish Chronic Toxicity Test

A chronic toxicity test of ballast water trea ted by Sunrui BWMS was conducted to Bareneck goby (Ctenogobius gymnauchen). The definitive tests were c onducted with 6.25%, 12.5%, 25%, 50% and 100% ballast water treated by Sunrui BW MS under the laboratory conditions. Test results indicated no chronic toxicity to survival and growth in Bareneck goby (Ctenogobius gymnauchen) at any test concentrations. The statisti cally determined LOEC and IC25 and actual NOEC were not measurable; the statistically determined NOEC was 100%. During the 7-day test period, the average survival of control an d treated larvae was greater than 80% and the growth rate of larvae in 6.25% , 12.5%, 25%, 50% and 100% ball ast water treated by Sunrui BWMS compared with control group were 99.6%, 100.5%, 101.0%, 99.8% and 100.2%, respectively. There is no significant statistical difference in survival and growth rate between control and treated groups.

The complete report of the aquatic toxicity test s is provided in appendix 4 of the confidential application dossier.

7.2.2 Determination of holding time (G9:5.2.7)

The holding time is the time that the treated ballast water has to be retained in the tanks to ensure there is no adverse effect concen tration upon discharge. Since th e neutralization step will be always employed in Sunrui BWMS treatment process prior to discharge, treated water can be discharged at anytime as long as the required disinfection level is achi eved. For the Sunrui BWMS, whether that level is achieved is de termined by the contact time between Active Substances and organisms. According to a series of biological efficacy tests, the retention time of 24 hours is considered to be adequate to meet regulation D-2.

7.3 Risk characterization and analysis (G9: 5.3)

7.3.1 Reaction with organic matter (G9: 4.2.1.3)

Major reactions of chlori ne with organic matter in polluted wa ter were described in section 4.3.4. THM and HAA identified as the major by-products of these reactions are dire ctly related to the total organic carbon in the water being treated and the chlorine dose level used for disinfection. As these by-products may bring risk to the enviro nment, they should be reduced to the minimum.

7.3.2 Characterization of degrad ation route and rate (G9: 5.3.5)

Degradation of TRO has two major routes: (1) through a quick consumption or decomposition by the chlorine demand in the pollu ted water (organic and nitrogen compounds, ions of Fe, Ni, Co that decompose TRO); and (2) through a slow decay via photolytic or heat decomposition.

Chlorine and all of its derive d species are oxidative and very reactive compounds. Chlorine gas is a more efficient oxidizer than hypochlorou s acid (HOCl), and hypochlorous acid is more efficient than the hypochlorite ion (ClO - 

### ). The balance between HOCl and ClO - 

### can be studied in polluted water with pH between 4 and 10. In this case, the kinetic of the reactions and the final products obtained depend for a large extent on th e percentage of each of the two species (HOCl, ClO - 

### ). The main reaction routes can be described as follows:

.1 Chlorination with amines R-NH 2 

### or ammonium NH 4 + 

### is very rapid and explains the very fast disappearance of available chlorine in waste water.

### MEPC 60/2/3 ANNEX Page 53

I:\MEPC\60\2-3.doc 

### .2 Oxidation reactions occur with many inorganic or organic compounds.

.3 Chlorination of C atoms from organic molecules is easier for molecules with a shorter carbon skeleton.

Three typical reactions are: reaction with phenol giving monochlor ophenols; reaction with molecules containing two carbon at oms: acetaldehyde, acetonitrile, and acetic acid, which are chlorinated on the CH 3 

### , and give chloroacetaldehydes, chloro acetonitriles and chloroacetic acids; and reaction with final degradati on of the carbon chain giving THMs.

HOBr/OBr - 

### is removed from seawater by several mechanisms. HOBr/OBr - 

### will react with natural organic matter to form tribromomethane by the haloform reaction. In fact, a number of disinfection products and other halogen containing compounds are reported when bromide is present in natural waters. Therefore, organic matter in ballast water could lead to the disappearance of the TRO. Sunlight can reduce HOBr/OBr - 

### to Br - 

### through a complex series of photochemical reactions. In some case s, where high concentrations of Cl - 

### are present, it may be that sunlight-mediated photolysis of HOBr /OBr - 

### leads to the formation of bromate ion. Therefore, photolysis may also lead to the loss of TRO. After the neut ralization and before the discharging, the concentrati ons of Active Substances and the bromate were 0 μg/L.

THMs are extensively removed in sewage treatmen t, probably primarily by volatilization as well as by degradation. All trihalomethanes are vola tile, the volatility decreasing in the order CHCl 3 

### > CHBrCl 2 

### > CHBr 2 

### Cl > CHBr 3 

### . Brominated acetic acids are ge nerally more biodegradable than their chlorinated counterparts. Relevant Chemicals and other chemicals are expected to be naturally degradable by natura l biotic or abiotic paths.

7.3.3 Prediction of discharge and envi ronmental concentrations (G9: 5.3.8)

7.3.3.1 Introduction

There were no Active Substances or bromate detected in treated ballast water after the neutralization and before the disc harging to receiving water, so that the Predicted Enviromental Concentration (PEC) for Active Substances and the bromate wase considered to be 0 μg/L in the harbour.

MAM-PEC Model of version 2.0 was used to calcula te the PEC of Relevant Chemicals and other chemicals in the port. MAM-PEC was originally programmed to calculate environmental concentrations of anti-fouling biocid es released from ship coatings.

In a modified way it can be used to calculate the concentrations that are re leased constantly into the water by other processes like for example ballast water treatment. The applicability of the model to any chemical substance made it a us eful tool for environmental impact studies.

7.3.3.2 Parameterization of the model

To calculate the environmental concentration of the released compound in the harbour water and the sediment, several parameters are necessary. These parameters define the harbour and its characteristics, the compound that is being rele ased and the amount of the specified compound released by ships. In the calculation, the OE CD-EU commercial harbour was chosen with the default setting given by MAM-PEC. Physico-ch emical property data for Relevant Chemicals and other chemicals were from Key Data Summary or calculation of the EPI suit. The input

### MEPC 60/2/3 ANNEX Page 54

I:\MEPC\60\2-3.doc 

### parameters were the same as input parameters of EUSES 2.1 which was used for human exposure assessment. The emission load was calculated from ballast water concentration for Relevant Chemicals and other chemical s and average amount of balla st water in the OECD-EU commercial harbour.

According to information contained in document BLG 13/INF.4, the daily ballast water discharge in port of Rotterdam (twice the size of th e OECD-EU commercial harbour) is about 100,000 m 3



### .

7.3.3.3 Half-life

Within MAM-PEC, it was not possible to include the decay of the compound of interest during emptying the ballast water tank. In this case, th erefore, a worst case scen ario was assumed that the water released from the ballast tanks has the sa me concentration at the start and at the end of discharge.

The ballast water was treated by filt er and electrolytic unit, and hol d in simulated tank for several days and then neutralized by sodium thiosulfat e. After the neutrali zation, the concentration of Active Substances and bromate was 0 μg/L in the ballast water, so the PEC of Active Substances and the Bromate in the harbour are 0 μg/L.

In the calculation of this dossier, using the worst case scenario, it is assumed that all chemicals will not decay in water of the harbour after disc harging. Predicted environmental concentrations (PEC) of the chemicals calculated by the MAM-PE C Model is based on the worst case scenario of 100,000 m 3 

### ballast water discharge.

The concentrations of Active S ubstances, Relevant Chemicals and other chemicals after the neutralization were measured during the analytic testi ng, as shown in Table 7-3.

Table 7-3: Maximum concentrat ion of chemicals detected in treated water at discharge

Chemicals Concentration, μg/L HOCl(NaOCl) 0 HOBr(NaOBr) 0 Chloramine 0 Tribromomethane 157.98 Dibromochloromethane 4.32 Monobromoacetic acid 3.31 Dibromoacetic acid 19.98 Tribromoacetic acid 41.63 Bromochloroacetic acid 0.61 Dibromochloroacetic acid 5.4 Dibromoacetonitrile 11.09 Bromate 0 Sodium thiosulphate 862

7.3.3.4 Harbour definitions

For all runs the OECD-EU commercial harbour wa s chosen with the default settings given by MAM-PEC. The modelling of the harbour is shown in Figure 7-9.

### MEPC 60/2/3 ANNEX Page 55

I:\MEPC\60\2-3.doc 

### Figure 7-9 : The modelling of the OECD-EU commercial harbour

Where:

x1 = 1,000 m y1 = 1,000 m x2 = 5,000 m y2 = 500 m depth = 15 m x3 = 2,500 m flow velocity = 1 m·s -1



### 7.3.3.5 Background concentration

The background concentration of HOCl( NaOCl), HOBr(NaOBr), Chloramine, Dibromochloromethane, Monobromoacetic acid, Tr ibromoacetic acid, Dibromochloroacetic acid, Dibromoacetonitrile, Bromate, Sodium thiosu lphate were measured to be 0μg/L and Tribromomethane, Dibromoacetic acid, Bromochlor oacetic acid were measured to be 0.19μg/L, 0.52μg/L and 0.19μg/L, respectively.

7.3.3.6 Results of Modelling

The PEC results from the MAM-PEC calcula tion are shown in Table 7-5. Maximum concentration was used in PEC/PNEC calculation. The data sheets are pr ovided in the relevant parts of appendix 8 in the conf idential application dossier.

Table 7-5: Estimated total concentrations for Active Substance and Relevant Chemicals by MAM-PEC (VER. 2.0 model)

Chemical name Maximum Concentration ( μ g/L) 95% Concentration ( μ g/L) Average Concentration ( μ g/L) Median Concentration ( μ g/L) Minimum Concentration ( μ g/L) HOCl(NaOCl) 0 0 0 0 0 HOBr(NaOBr) 0 0 0 0 0
Chloramine 0 0 0 0 0
Tribromomethane 1.64E+00 1.61E+00 6.94E-01 3.22E-01 2.08E-01
Dibromochloromethane 3.09E-02 3.01E-02 1.11E-02 3.32E-03 4.79E-04
Monobromoacetic acid 3.03E-02 2.97E-02 1.06E-02 2.78E-03 3.72E-04
Dibromoacetic acid 7.03E-01 6.99E-01 5.84E-01 5.37E-01 5.22E-01
Tribromoacetic acid 3.81E-01 3.74E-01 1.33E-01 3.49E-02 4.68E-03

### MEPC 60/2/3 ANNEX Page 56

I:\MEPC\60\2-3.doc Chemical name Maximum Concentration ( μ g/L) 95% Concentration ( μ g/L) Average Concentration ( μ g/L) Median Concentration ( μ g/L) Minimum Concentration ( μ g/L) Bromochloroacetic acid 1.96E-01 1.95E-01 1.92E-01 1.91E-01 1.90E-01
Dibromochloro acetic acid 4.94E-02 4.85E-02 1.72E-02 4.53E-03 6.07E-04
Dibromoacetonitrile 1.02E-01 9.95E-02 3.54E-02 9.30E-03 1.25E-03
Bromate 0 0 0 0 0 Sodium thiosulphate 7.62E+00 7. 47E+00 2.67E+00 7.07E-01 9.68E-02



### 7.3.4 Assessment of potential for bioaccumulation (G9:5.3.7)

As the logarithm octanol/water partition coeffici ents (log Pow) of all Active Substances, Relevant Chemicals and other chemicals in th e treated ballast water by Sunrui BWMS are < 3 and the BCFs of all chemicals are below 500 L/kg, there is no need to assess the potential for bioaccumulation in marine or freshwater or ganisms in accordance with Procedure (G9), paragraph 5.3.7.

7.3.5 Effects assessment

The toxicity data sets (Tables 4-1 and 4-2) indicate that the risk of the Active Substances of HOCl is significant for most freshwater and saltwater predat ors (fish) and primary producer (alga) based on a chronic NOEC <0.01 mg/L.

The ecological risk of the Relevant Chemicals to aquatic organisms is less than the risk from the Active Substances because much less chroni c NOEC toxicity data are available. Chronic data of two trophic levels used in this dossier are available for tribromomethane and bromate to conclude that the compounds shoul d not be a risk to predators a nd alga because all of the NOECs are 2-3 orders of magnitude above 0.01 mg/L. Likewise, one chronic crustaceans value (1.6 mg/L) is available for monobromoacetic ac id. An NOEC of 600 mg/L was found for fish exposed to sodium thiosulphate which indicates that the risk of sodium thio sulphate is negative. Because of the lack of a comple te chronic database for (i.e., one or more of the three chronic trophic levels used in this dossier are not available) , a great deal of uncertainty exists for some of the THMs and HAAs. In addition, one must also consid er the fact that it is unlikely that only one chemical will be discharged in the ballast water. Additional risks are likely when a mixture of the relevant chemicals is discharged.

7.3.6 Effects on aquatic organisms

In chemical testing, no potential ecotoxic substa nce was found in the treated water. Predicted No-Effect Concentrations (PNEC) values were calculated using the aquatic toxicity data-set endpoints and the appropriate asse ssment factor. The calculation results are shown in Table 7-6.

### MEPC 60/2/3 ANNEX Page 57

I:\MEPC\60\2-3.doc 

### Table 7-6: PNEC for the Active Substances and Relevant Chemicals in freshwater and saltwater according to data-set endpoint

Chemical name Toxicity (mg/L) Information Assessment factor PNEC (mg/L) HOCl(NaOCl) 0.003 Lowest L(E)C50 from a fish, crustacean and alga and lowest NOEC from a algae, crustaceans and fish 100 0.00003

Chloramine 0.012 Lowest LC50 from a fish and crustacean 1000 0.000012
Tribromomethane 4.8 Lowest L(E)C50 from a fish, crustacean and alga and Lowest NOEC from a algae and fish 100 0.048

Dibromochloromethane 3.2 Lowest L(E)C50 from a fish, crustacean and alga and Lowest NOEC from fish 100 0.032

Monobromoacetic acid 0.2 Lowest L(E)C50 from a crustacean and alga and Lowest NOEC from crustacean 1000 0.0002

Dibromoacetic acid 6.9 Lowest LC50 from a fish 1000 0.0069
Tribromoacetic acid 6.9 PNEC was assumed to be the same value as that for dibromoacetic acid 1000 0.0069

Bromochloroacetic acid 6.9 PNEC was assumed to be the same value as that for dibromoacetic acid 1000 0.0069

Dibromochloroacetic acid 6.9 PNEC was assumed to be the same value as that for dibromoacetic acid 1000 0.0069

Dibromoacetonitrile 0.55 Lowest L(E)C50 from a fish, crustacean and alga 1000 0.00055

Bromate 8 Lowest L(E)C50 from a fish, crustacean and alga and Lowest NOEC from fish and alga 100 0.08

Sodium thiosulphate 64 Lowest L(E)C50 from a fish and alga and Lowest NOEC from fish 1000 0.064



### Risk to aquatic environment by chemicals in ballast water was carried out by calculating PEC/PNEC ratio. If PEC/PNEC ratio is less than or equal to 1, the chemical is of no immediate concern. In PEC/PNEC ratio is greater than 1, the substance should be of concern. Active Substances were not detected in treated ball ast water so that risk assessment to aquatic environment for Active Substance was not consider ed. PNEC values are normally derived from short-term and/or long-term aquatic toxicity results for relevant aquatic species by dividing the lowest available effect concentration with an appropriate assessment factor.

The PEC/PNEC calculated for chemicals are all le ss than 1, so the ballast water treated by Sunrui BWMS has low potential risk for aquatic environment. Risk assessment results for aquatic environment are summarized in Table 7-7.

### MEPC 60/2/3 ANNEX Page 58

I:\MEPC\60\2-3.doc 

### Table 7-7: Risk assessment results for aquatic environment

Chemicals PEC/PNEC
Tribromomethane 0.03417
Dibromochloromethane 0.00097
Monobromoacetic acid 0.15150

Dibromoacetic acid 0.10188
Tribromoacetic acid 0.05522
Bromochloroacetic acid 0.02841
Dibromochloroacetic acid 0.00716
Dibromoacetonitrile 0.18545 Sodium thiosulphate 0.11906



### 7.3.7 Effects on sediment

As stated in section 4.1.4, the Koc values of all chemicals range from 2.7×10 -8 

### to 468, which are smaller than 500 l/kg, which indicate that the chemi cals will not readily partition to sediment and thus be of concern to benthic or ganisms residing in the sediment, so the risk to infaunal sediment organisms is low.

7.3.8 Comparison of effect asse ssment with discharge toxicity

The concentration of Active Substance, Relevant Chemicals and other chemicals in the ballast water were measured by analytical methods and th e aquatic toxicity tests were conducted using the same ballast water. From the toxicity test results, no mortality an d adverse effects were observed, so the toxic effects of the ballast wate r treated by Sunrui BWMS to aquatic organisms would be low.

8 RISK ASSESSMENT

8.1 Risk to safety of ship

8.1.1 Flooding

The Sunrui BWMS is connected to the ship ba llast piping system by ha rd rubber lined steel pipes, together with a number of electromagneti c and manual valves. The piping to connect the BWM system with ship ballast piping system is designed and arranged in accordance with the classification rules. The BWM system is so designed that in case of any failure of the components or function module, the system w ill be stopped automatically to isolate the BWM system from the ship ballast piping. Manual va lves are also f itted in the system so that the BWM system can be closed by the manual valves if there is a failure of the automatic valves.

8.1.2 Corrosion

The corrosivity evaluation for th e ballast water treated by elec trolysis were reported by some previous applicants in documents MEPC 58/2, annex, page 63, MEPC 59/2/6, annex, page 20 and MEPC 59/2/11, annex, page 68. These documents in dicated that water treat ed by electrolysis would have no significant increased corrosion co mpared to natural seawater, and even less

### MEPC 60/2/3 ANNEX Page 59

I:\MEPC\60\2-3.doc 

### corrosive than natural seawater in some cases. In particular, it has been noted that document MEPC 58/2/7, (GESAMP-BWWG 6, annex 7, paragr aph 4.7.2) indicated an electrolysis system with an initial TRO concentrations up to 10 ppm did not have increased corrosion effect. The system mentioned above also reported that the test barge with coated ball ast tanks, after 2 years of undefined usage rate, did not in dicate increased corrosion effect.

Some initial corrosion experiments have been c onducted to evaluate the corrosion of treated ballast water by Sunrui BWMS according to Procedure (G9) and the Methodology. The tests include uncoated steels and coated steel.

The corrosion rates of bare steels were tested using the method of mass loss. No localized corrosion was found on the samples of 360 steel and CCS B steel both in the treated water and in the control water. The corrosion tests show th at the corrosion morphology of the bare samples subjected to the treated water are same to those subjected to natura l seawater, i.e., all are uniform corrosion. The results of corrosion rate calculati on indicate that the corr osion rate of the bare steels in the ballast water treated by Sunrui BWMS is at the similar level with that of the steels in natural seawater.

The test report is given in appendix 5. In th is connection, it should be noted that hard rubber lined steel pipe is used to conne ct the electrolysis unit with the main ballast piping in order to prevent corrosion.

The test for coated steel has not completed since the specimens need to be tested for the duration of 6 months. Therefore, the test results for co ated steel will be provided in the application for Final Approval.

Further corrosion testing will be conducted taking into consid eration the recommendations provided by the GESAMP-BWWG at its eighth mee ting and the testing results will be provided in the application for Final Approval.

8.1.3 Fire and explosion

The only chemical carried on board is sodium thiosulfate for neutrali zing residual TRO during de-ballasting. The solution is stored in a sealed PVC container, which is neither flammable nor explosive.

8.1.4 Hydrogen gas and Chlorine gas

Hydrogen gas

Hydrogen gas is generated during the electrolytic process. Th eoretically, under the condition of the TRO concentration of 9.5 ppm (the maxi mum allowable dosage of TRO), 133.8 mol of hydrogen gas (H 2 

### ) is generated in the electrolysed water with concentrated TRO for treating 1,000 ton of ballast water, which equals 267.6 g.

The electrolysed water entraining H 2 

### gas is entered into the degas tank. H 2 

### gas is fully separated inside the tank, and diluted by air blowers to the level below Lower Explosive Limit (LEL). Then, the diluted gas is released overboard. A spark arre stor is fitted on the discharge end of vent pipe.

### MEPC 60/2/3 ANNEX Page 60

I:\MEPC\60\2-3.doc 

### Rated air flow of the blowers is calculated accordi ng to the relevant specifi cations to ensure that the volume of air provided is adequate to dilute H 2 

### gas to the leve l below LEL. Considering it is important to supply air continuously , two air blowers are fitted in the degas unit. Should the one in operation fail, the other one will continue to operate automatically.

During the land-based tests, H 2 

### gas was monitored, but no hydrogen gas was ever detected in the area around the electrolytic unit or in the headspace of the treated tank. Nevertheless, as a further safety measure, an air pressure sensor is instal led at the discharge side of the blowers, and the sensor will send an acousto-optic alarm in the case of insufficient of air supply.

The technology for venting hydrogen gas has been employed by Sunrui Company in the design and manufacture in relati on to electrolysis process for several hundreds of the inst allations either onboard (sewage water treatment system by elec trolytic method) or in land-based systems (antifouling of seawater cooling system). These installations ha ve been in operation safely and reliably for many years.

Chlorine gas The chlorine gas produced by elec trolysis dissolves into seawat er rapidly, generating active substances (TRO). The short-term exposure limit of chlorine gas is known to be 1 mg/m 3 

### (MSDS, approximately 0.78 ppm). Under normal ope ration, chlorine gas will not leak from the BWM system. During the tests, no chlorine gas wa s detected in the area around the electrolytic unit, and the chlorine gas concentrations in the headspace of treated tank were measured below 0.3 ppm immediately after electrolytic treatment, which clears away rapidly.

To monitor the accidental leakage of hydrogen gas and chlorine gas, hydrogen gas and chlorine gas, sensors and alarms are included in the BWMS to detect any leakage online. Acousto-optic alarms will be sent when the concentrations of H 2 

### and Cl 2 

### exceeding 2% and 0.4 ppm, respectively. If the concentrations of H 2 

### and Cl 2 

### exceed 3% and 0.55 ppm, respectively, the electrolytic units will be imme diately shut down automaticall y. Meanwhile, ventilation will continue by air blowers to dilute H 2 

### to the level below Lower Explosive Limit.

When an alarm signal activates, relevant informati on and instructions on the remedy measures to be taken will be given on the human-machine interface (HMI).

8.1.5 Storage and handling of the substances

The only chemical substance carried on board is s odium thiosulfate. The substance is widely used in dechlorination in water, such as halt ble aching in the paper-making industry. It is also used in smelting silver ore, in producing leather goods and to se t dyes in textiles. Sodium thiosulfate is also used to fix black and white photography negatives afte r the developing stage.

Sodium thiosulfate is kept in a tightly closed co ntainer, stored in a cool, dry, ventilated area, therefore, there is no any risk to the safe ty of ships during storage and handling it.

When the sodium thiosulfate is handled and mixed by crew, it is required that the operators should wear protective gloves, clean body-coveri ng clothing and safety glasses. Safety procedure for handling of sodium thiosulfate is detailed in Technical Specification and Manual, in appendix 9 of the full application dossier.

### MEPC 60/2/3 ANNEX Page 61

I:\MEPC\60\2-3.doc 

### 8.1.6 Noise

The Sunrui BWMS operates in engine room of th e ships using standard pumps and valves, which will be tested against noise standard duri ng type approval by the Classification Society.

8.2 Risks to human health

Risk to human health introduced from the di scharged water was evaluated by using EUSES (version 2.1) to achieve detail ed assessment data. A Human Exposure Scenario (HES) via seafood consuming was conducted according to EUSES.

The results of risk assessment show that ratio MOS/Reference MOS (MRR) for the chemicals in ballast water is > 1 for general population in local a nd regional scale. Th erefore, the ballast water treated by Sunrui BWMS has low potential ri sk to human health. Data sheets of EUSES are contained in the relevant pa rts of appendix 8 of the confid ential application dossier. The results are showed in Table 8-3.

Table 8-3: MRR (MOS/MOSref) values

Chemical Name PEC,
μ g/L BCFfish,

m 3 

### /kgwwt Cfish, mg/kg MRR

Tribromomethane 1.64 14 2.30E-02 4.75E+03
Dibromochloromethane 0.0309 1.47 4.54E-05 1.88E+05
Bromoacetic acid 0.0303 3.20 9.70E-05 3.14E+05
Dibromoacetic acid 0.703 0.17 1.20E-04 6.34E+04
Tribromoacetic acid 0.381 0.63 2.40E-04 1.01E+05
Bromochloroacetic acid 0.196 3.20 6.27E-04 1.94E+04
Dibromochloroacetic acid 0.0494 3.16 1.56E-04 2.93E+05
Dibromoacetonitrile 0.102 3.00 3.06E-04 1.99E+03
Sodium thiosulfate 7.62 3.16 2.41E-02 1.39E+04

8.3 Risks to the aquatic environment

Risk to aquatic environment intr oduced by chemicals in discharged ballast water was accessed by the calculation of PEC/PNEC ratio . When PEC/PNEC ratio is less than or equal to 1, the chemical is considered to be not of immediate concern. When PEC/ PNEC ratio is greater than 1, the substance should be of concern.

The PEC/PNEC calculated for chemi cals are all less than 1, so the ballast water tr eated by Sunrui has low potential risk for aquatic environm ent. Detailed results are shown in 7.3.6.

9 ASSESSMENT REPORT (G9: 4.3)

9.1 Test report data quality

The ballast water treated by Sunr ui BWMS have been tested by the following organizations in accordance with the relevant intern ational recognized guidelines, and the data obtained from the testing were used in the dossier fo r the application of Basic Approval:

### MEPC 60/2/3 ANNEX Page 62

I:\MEPC\60\2-3.doc 

### .1 Aquatic toxicity tests were conducted by Supervision and Test Center for Pesticide Safety Evaluation and Quality Control (PSEC) in Shenyang. PSEC is accredited for toxicological safety evaluations of drugs, pesticides, and other fine chemicals by Ministry of Agriculture of the People Republic of China.

.2 The chemical analysis was performe d by PONY Testing International Group in Qingdao and Beijing labor atories (PONY TEST).

.3 The measuring of environmental paramete rs of the seawater and the physical and chemical properties of the treated ballast water were carried out by the Center of Marine Environmental Measurement, the first institute of Oceanography, State Oceanic Administration.

.4 The corrosion tests were conducted by Qingdao Laboratory for Corrosion and Protection, CSIC Luoyang Ship Material Re search Institute Testing & Calibration Center.

The above four organizations are accredited by China National Accreditation Service for Conformity Assessment (CNAS, eqv. to ISO/ IEC 17025 ) and China Metrology Accreditation (CMA). In addition, PSEC is registered as a Good Laboratory of Practice (GLP) laboratory in China and run in accordance with the requirements of GLP lab.

These organizations are all qualified testing organizations, and have their own Quality Management Plan (QMP). The testing plans and QAPPs for the aquatic toxicity tests, chemical analysis, measurements of parameters of the seawater and corrosion tests were developed and strictly followed thr ough all the tests.

REFERENCES

A.I.S.E. March 1997. Technical Task Force H yppochlorite: benefits a nd safety aspects of hypochlorite formulated in domestic products.

ATSDR (Agency for Toxic Substances and Dis ease Registry). September 2003. Bromoform and dibromochloromethane CAS# 75-25-2 and 124-48-1.

Bashtan S. Yu., Goncharuk V.V., Chebotareva R.D. et al. 1999. Production of sodium hypochlorite in an electrolyser equipped with a ceramic membra ne. Desalination, Volume 126, Issues 1-3, pages 77-82.

Bengt A.J.Kallen, Elisabeth Robert. 2000. Dri nking water chlorination and delivery outcome ñ a registry-based study in Sweden. Repr oductive Toxicology, Vo lume 14, pages 303-309.

Canadian Council of Ministers of the Environmen t, 1999. Canadian water quality guidelines for the protection of aquatic life- reactive chlorine species.

Carlos Estrela, Cyntia R.A. Estrela, Eduardo Luis Barbin, et al. 2002. Mechanism of Action of Sodium Hypochlorite. Brazilian De ntal Journal, 13(2), pages 113-117.

Cerkinskij S.N., Trahtman N. 1972. The present status of research on the disinfection of drinking water in the USSR. Bull.Org.mond.S ante; Bull. Wld Hlth Org., 46, pages 277-283.

### MEPC 60/2/3 ANNEX Page 63

I:\MEPC\60\2-3.doc 

### Chizuko Morita, Kouichi Sano, Shinichi Morimatsu., et al. 2000. Disinfection potential of electrolyzed solutions containing sodium chloride at low concentrations. Journal of Virological Methods, Volume 85, Issues 1-2, pages 163-174.

Department of environmental prot ection, Florida. May 1998. Bioassays of Arrowhead campground wastewater treatment plant.

DeQueiroz G.A. and Day D.F. 2008. Disinfection of bacillus subtilis spore- contaminated surface materials with a sodium hypochlorite and a hydr ogen peroxide-based sanitizer. Letters in Applied Microbiology, 46, pages 176-180.

Documentation of OEL : Bromoform . Jour nal of Occupational Health 2000,42, pages 229-233.

Drogui P., Elmale h S., Rumeau M., et al. 2001. Oxidizing and disinfec ting by hydrogen peroxide produced in a two-electrode cell. Wate r Research, Volume 35, Issue 13, pages 3,235-3,241.

Edstrom Industries. Chlorinati on of Drinking Water. 4230-M14174, www.edstrom.com

. EPA. Information about Chloramine in Drinking Water.

EPA. March 1994. Drinking water criteria docume nt for chloramines. Health and ecological criteria division office of scie nce and technology office of water. Final draft, ECAO-CIN-D002.

Euro Chlor. December 2006. Euro chlor risk assessment for the marine environment OSPARCOM Region-North Sea : Monochlorom ethane. Marine risk assessment.

European Commission ,Scientific Committee on Health and Envir onmental Risks. January 2008. Risk assessment report on sodi um hypochlorite Human health pa rt, CAS No.:7681-52-9 EINECS No.231-668-3.

Exon J.H., et al. 1987. Immunotoxicologic evaluation of chlorine-based drinking water disinfectants, sodium hypochlor ite and monochloramine. Toxico logy, Volume 44 , pages 257-269.

F. John Upsher and Lyn E. Fletcher. March 199 6. Review of Chlorine and Organohalides and their significance to The Royal Australian Navy . Defence science and technology organisation, DSTO-TR-0311.51pp.

Fisher D.J., Burton D.T., Yonkos L.T., et al. Acute and Short-Term Chronic Effects of Continuous and Intermittent Chlorination on Mysi dopsis bahia and Menidia beryllina. Environ. Toxicol. Chem.13(9), pages 1,525-1,534.

Frerichs G.N., Tweedie A., Starkey W.G. and Richards R.H. 2000. Temperature, pH and electrolyte sensitivity, and heat , UV and disinfectant inactivati on of sea bass (Dicentrarchus labrax) neuropathy nodavirus. Aquaculture, 185, pages 13-24.

Fumiaki Hamaguchi and Takeki Tsutsui. 2 000. Assessment of genot oxicity of dental antiseptics: ability of phe nol,guaiacol, p-phenolsulfonic acid, sodium hypochlorite, p-chlorophenol, m-cresol or formaldehyde to induce unscheduled DNA synthesis in cultured Syrian hamster embryo cells. Japanese Jour nal of Pharmacology, Volume 83, pages 273-276.

### MEPC 60/2/3 ANNEX Page 64

I:\MEPC\60\2-3.doc 

### Geo. Clifford White. 1998. Handbook of chlorinatio n and alternative disinf ectants. Chapter 4, Chemistry of chlorination. Thir d Edition, New York. Pages 184-249.

George R. Douglas, Earle R. Nestmann, and Guy Le bel. 1986. Contribution of chlorination to the mutagenic activity of drinking water extracts in Salmonella and Chinese hamster ovary cells. Environmental Health Perspectives, Vol.69, pages 81-87.

Giller S., Le-Curieux F., Erb F. and Marzin D. 1997. Comparative genotoxicity of halogenated acetic acids found in drinking water, Mutagenesis, 12(5), pages 321-328.

Goodman L.R., Middaugh D.P., Hansen D.J., Higdon P.K., and Cripe G.M. 1983. Early Life-Stage Toxicity Test with Tidewater Silversides (Menidia peninsulae) and Chlorine-Produced Oxidants, Environmental To xicology and Chemistry, Vol. 2, pages 337-342.

Health Protection Agency. 2007. HPA Compendium of Chemical Hazards: Chlorine. Version 2.

Heitmuller P.T., Hollister T.A., and Pa rrish P.R . 1981. Acute toxicity of 54 industrial chemicals to sheepshead minnows (Cyprinodon variegatus).Bull. Environm. Contam. Toxicol., 27, pp 596-604.

Hong-Xing Shi, Jiu-Hui Qu, Ai-Min Wang a nd Jian-Tuan Ge. 2005. Degradation of microcystins in aqueous solution with in situ electrogenerated active chlorine. Chemosphere, Volume 60, Issue 3, pages 326-333.

HPA (Health Protection Agency). 2007. Sodium hypochl orite Toxicological overview. Version 1.

IARC. BROMOFORM. IARC monogr aphs volume 71, pages 1309-1316.

IMO (International Maritime Organization). 12 December 2008. Harmful Aquatic Organisms in Ballast Water. MEPC 59/2/6.

IMO (International Maritime Organization). 19 December 2008. Harmful Aquatic Organisms in Ballast Water. MEPC 59/2/11.

IMO (International Maritime Organization). 20 December 2007. Harmful Aquatic Organisms in Ballast Water. MEPC 57/2/7.

IMO (International Maritime Organization). 20 March 2008. Harmful Aquatic Organisms in Ballast Water. MEPC 58/2.

Jih-Terng Wang, Ming-Hui Chen, Hung-Jen Lee, et al. 2008,9. A model to pred ict total chlorine residue in the cooling se awater of a power plant using iodine colorimetric method. International journal of molecular sciences, pages 542-553.

John R.Meier, H.Paul Ringhand, W.Emile Coleman et al. 1986. Mutagenic by-products from chlorination of humic acid. Environmental Health Perspectives, Vol.69, pages 101-107.

Joyce E., Mason T.J., Phull S.S. and Lorimer J.P. 2003. The development and evaluation of electrolysis in conjunction with power ultrasound for the disinfect ion of bacterial suspensions. Ultrasonics Sonochemistry, Volu me 10, Issues 4-5, pages 231-234.

### MEPC 60/2/3 ANNEX Page 65

I:\MEPC\60\2-3.doc 

### LeBlanc G.A. 1980. Acute Toxicity of Prior ity Pollutants to Water Flea (Daphnia magna), Bull.Environm.Contam.Toxi col., 24, pages 684-691.

Leo Kunigk., et al. Jun.2008. Hypochlorous aci d loss from neutral electrolyzed water and sodium hypochlorite solu tions upon storage. Brazilia n Journal of Food Technolo gy, v .11, n . 2, pp 153-158.

Mabey W., and Mill T. 1987. Cr itical review of hydrolysis of organic compounds in water under environmental conditions, J. Phys. Chem. Ref .Data, Vol 7, No.2, pages 383-415.

Marten de Vries v, Peter R. Massolt v. 2006. Evaluation of a new method for ballast water treatment. Pages 1-7.

Michiko Nishimura, Naoyuki Kariya, Ulamnemekh Hulan., et al. 2004. Comparison of the hand disinfectant effects between super hypochlorou s water and 7.5% povidone -iodine. Pediatric Dental Journal, 14(1), pages 1-3.

Migliore L., Tancioni L., et al. Ecotoxicity testing of Tiber Rive r water as compared to ClO2, NaClO & PAA.

Milko A. Jorquera, Gustavo Valencia, Mitsuru Eguchi., et al. 2002. Disinfection of seawater for hatchery aquaculture sy stems using electrolytic water treat ment. Aquaculture, Volume 207, Issues 3-4, pages 213-224.

National Standard of the Peopleís Republic of China. 2006. GB 5749-2006
, Standards for drinking water quality.

Norihito Nakajima, Takashi Nakano, Fumiue Harada., et al. 2004. Evaluation of disinfective potential of reactivated free chlorine in poo led tap water by electrolysis. Journal of Microbiological Methods, Volu me 57, Issue 2, pages 163-173.

Petkov L., Todorov T.. 2006. Dardanova I. and Bo shnakov K. Mathematic al modelling of the process of electrochemical production of NaClO fr om diluted chloride solutions. Journal of the University of Chemical Technology and Metallurgy, 41(2), pages 133-136.

Reproductive and Cancer Hazard Assessment Secti on Office of Environmental Health Hazard Assessment (OEHHA), California E nvironmental Protection Agenc y. June 2003. No significant risk level (NSRL) for the propositi on 65 carcinogen bromoform. OEHHA.

Richard F. Shaw and Kevin W. Baggett. December 2006. Annotated Bibliography of the Potential Environmental Impacts of Chlorina tion and Disinfection Byproducts Relevant to Offshore Liquefied Natural Gas Po rt Facilities.OCS Study MMS 2006-071.

Ross M.P., et al. April 1999. Fatal ingestion of sodium hypochlorite bleach with associated hypernatremia and hypochloraemic metabolic acidosis. Veterinary and Human Toxicology, 41 (2), pages 82-86.

Tapas K. Das. 2002,4. Evaluating the life cy cle environmental performance of chlorine disinfection and ultraviolet technologies. Clean Techn Environ Policy, pages 32-43.

### MEPC 60/2/3 ANNEX Page 66

I:\MEPC\60\2-3.doc 

### Trass T.P. and Bontje D.M. 2005. Environmenta l risk limits for alcohols, glycols, and some other relatively soluble and/or volatile compounds 2.I ntegration of human and ecotoxicological risk limits. RIVM report 601501027.

U.S. Department of health and human servi ces public health service Agency for Toxic Substances and Disease Registry. August 2005. Toxicological profile for bromoform and dibromochloromethane.

Vijayaraghavan K., Ramanujam T.K. and Balasubr amanian N. 1999. In situ hypochlorous acid generation for the treatment of syntan wastew ater. Waste Management, Volume 19,Issue 5, pages 319-323.

WHO (World Health Organiza tion). 1996. Chloroacetones in drinking-water, Background document for development of WHO Guidelin es for Drinking-water Quality. Geneva, WHO/SDE/WSH/03.04/50.

WHO (World Health Organization). 2000. Envir onmental health criteria 216, Disinfectants and disinfectant by-products. World Health Organization, Geneva.

WHO (World Health Organizatio n). 2004. Brominated Acetic Acids in Drinking-water, Background document for development of WHO Gu idelines for Drinking-water Quality. WHO/SDE/WSH/03.04/79.

WHO (World Health Organization) . 2004. Guidelines for drinki ng-water quality, Geneva.Third edition, Volume 1.

WHO (World Health Organization). Disinf ectants and Disinfection By-Products. WHO SEMINAR PACK FOR DRI NKING-WATER QUALITY.

Williamson K.S. 1967. A prognostic study of o ccupational dermatitis cases in a chemical works. British Journal of Industria l Medicine, Volume 24 , pages 103-113.

Yuji Kurokawa, Shozo Takayama,Yoichi Konishi, et al . 1986. Long-term in vivo carcinogenicity tests of potassium bromate,sodium hypochlorite, and sodium chlorite conducted in Japan. Environmental Health Perspectives, Volume 69, pages 221-235.

Zargar S., Ghosh T.K. 2007. Thermal and Biocid al (Chlorine) Effects on Select Freshwater Plankton. Archives of Environmental C ontamination and Toxicology, 53, pages 191-197.

___________