I:\MEPC\57\2-6.doc 

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

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

INTERNATIONAL MARITIME ORGANIZATION

IMO 

E

MARINE ENVIRONMENT PROTECTION 

COMMITTEE 

57th session 

Agenda item 2 

MEPC 57/2/6

 7 September 2007

 Original: ENGLISH

HARMFUL AQUATIC ORGANISMS IN BALLAST WATER 

Application for Basic Approval of a ballast water management 

system using Active Substances 

Submitted by Norway 

SUMMARY

Executive summary: This document contains non-confidential information for 

Basic Approval of a ballast water management system under the 

Procedure for approval of ballast water management systems that 

make use of Active Substances (G9) adopted by resolution 

MEPC.126(53). The documentation complies with the requirements 

related to assessments for Basic Approval. 

Action to be taken: Paragraph 5 

Related documents: BWM/CONF/36; MEPC 53/24/Add.1, and BWM.2/Circ.10 

Introduction 

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

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

comply with the Convention shall be approved by the Organization. 

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

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

(MEPC 53/24/Add.1, annex 4, paragraph 4.2.1) and provisions for risk characterization and 

analysis (MEPC 53/24/Add.1, annex 4, paragraph 5.3). Section 6 of the Procedure (G9) presents 

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

provided in the application. 

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

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

Procedure (G9) adopted by resolution MEPC.126(53). 

4 Norway therefore submits the non-confidential part of the manufacturerís application 

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

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

GESAMP-Ballast Water Working Group for their fourth meeting with the understanding of 

confidential treatment. 
MEPC 57/2/6 - 2 - 

I:\MEPC\57\2-6.doc 

Action requested of the Committee 

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

***
MEPC 57/2/6 

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ANNEX 

NONñCONFIDENTIAL PART OF MANUFACTURERíS 

APPLICATION DOSSIER 

The applicant proposes a ballast water management system (BWMS), comprised of a number of 

different processes which include the use of Active Substances for the deactivation of organisms 

in shipís ballast water. This deactivation is achieved through the use of cavitation, nitrogen 

supersaturation and disinfection. The disinfective Active Substances are produced by an 

electrodialytic technology sometimes referred to as electrochemically activation of water. 

 

This application is based on the Procedure for approval of ballast water management systems 

that make use of Active Substances (G9) and GESAMP-BWWG Draft Methodology 

(MEPC 56/2/2, annex 4). 

Table of Contents 

1 INTRODUCTION 

1.1 Overview 

1.2 Current status 

2 THE OCEANSAVERÆ BWMS: MAIN COMPONENTS 

2.1 Layout 

2.2 The Mechanical Filtration Unit 

2.3 The C3t Unit 

2.4 The C2e Unit 

2.4.1 Overall description of the unit 

2.4.2 Electrochemical activation 

2.5 Nitrogen Supersaturation Unit 

2.6 Control & Auxiliary equipment 

3 ACTIVE SUBSTANCES AND RELEVANT CHEMICALS 

3.1 Definitions 

3.2 Active Substances 

3.3 Relevant Chemicals 

3.3.1 Reaction between Active Substance and bromide ions 

3.3.2 Reaction between Active Substance and nitrogen compounds 

3.3.3 Reaction between Active Substance and organic compounds 

3.4 Other chemicals 

4 DATA SET FOR ACTIVE SUBSTANCES AND RELEVANT CHEMICALS 

4.1 Overview of Active Substances and Relevant Chemicals 

4.1.1 Active Substances 

4.1.2 Relevant Chemicals 

4.1.3 Other chemicals 

4.1.4 Structural formula 
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4.2 Physical and chemical properties for the Actives Substances and Preparations and treated 

ballast water 

4.2.1 Active Substances 

4.2.2 Relevant Chemicals 

4.3 Data on environmental fate and effects under aerobic and anaerobic conditions 

4.3.1 Modes of degradation 

4.3.2 Bioaccumulation, partition coefficient, octanol/water partition coefficient 

4.3.3 Persistence and identification of the main 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 Interactive effects 

4.4 Effects on aquatic plants, invertebrates, fish and other biota 

4.4.1 Hypochlorous acid 

4.4.2 Hydrogen peroxide 

4.4.3 Ozone 

4.4.4 Chlorine dioxide 

4.4.5 Bromoform 

4.4.6 Dibromochloromethane 

4.4.7 Dichlorobromomethane 

4.4.8 2,4,6-Tribromophenol 

4.4.9 Dibromoacetonitrile 

4.4.10 Monobromoacetic acid 

4.5 Data on mammalian toxicity 

4.5.1 Hypochlorous acid 

4.5.2 Hydrogen peroxide 

4.5.3 Ozone 

4.5.4 Chlorine dioxide 

4.5.5 Bromoform 

4.5.6 Dibromochloromethane 

4.5.7 Dichlorobromomethane 

4.5.8 2,4,6-Tribromophenol 

4.5.9 Dibromoacetonitrile 

4.5.10 Monobromoacetic acid 

5 HANDLING AND USE OF THE OS BWMS 

5.1 General 

5.2 Circumferential cavitation - C3T 

5.3 The C2E Unit 

5.3.1 Training 

5.3.2 Fire fighting measures 

5.3.3 Safety issues ñ precautions 

5.4 Handling and use of the nitrogen supersaturation unit 

5.4.1 General 

5.4.2 Precautions to be observed at all times 

5.4.3 Training 

5.4.4 Handling and storage 

5.4.5 Emergency measures 
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6 RISK CHARACTERIZATION 

6.1 Screening for Persistency, Bioaccumulation and Toxicity 

6.1.1 The P criterion 

6.1.2 The B criterion 

6.1.3 The T criterion 

6.2 PEC ñ PNEC assessment 

6.2.1 PNEC estimation 

6.2.2 PEC values in discharged ballast water 

6.2.3 PEC ñ PNEC estimation 

6.3 Ecotox testing of treated ballast water 

6.3.1 Ecotox testing of similar systems 

6.3.2 Initial ecotox testing of ballast water treated with OS BWMS 

7 RISK ASSESSMENT 

7.1 Risk to safety of ship 

7.1.1 Ballast water tanks 

7.1.2 Ballast water pipe systems 

7.2 Risk to human health 

7.2.1 General 

7.2.2 Precautions to be observed at all times 

7.2.3 Hazards identification 

7.2.4 Emergency Measures 

7.2.5 Emergency First Aid 

7.3 Risk to the aquatic environment 

8 REFERENCES 
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1 INTRODUCTION 

1.1 Overview 

The applicant proposes a combined ballast water management system (BWMS) that applies 

cavitation, supersaturation and disinfection as main working principles following a pre-filtration 

step. The system, OceanSaverÆ BWMS (OS BWMS), is the result of the merging of two 

independent research projects, following recommendations by the Norwegian Research Council. 

Initially, both projects were established to develop a complete BWMS, the common denominator 

being the inclusion of nitrogen supersaturation. 

The OS BWMS is constructed of several components which may be categorized as both ancillary 

components and as OceanSaverÆ components. The ancillary components are industrial-type 

equipment developed for, and are in operation on board ships worldwide. For these components, 

the OS BWMS is not committed to using a singular manufacturer or a specific component, but 

rather it is more pertinent to specify equipment performance and deliverables. The OceanSaverÆ

components, on the other hand, are specifically developed and designed for the OS BWMS and 

thus require a more in-depth specification. 

The first component in the OS BWMS is a mechanical filtration component which pre-filters 

particles and organisms to the order of tens of μm (depending on filter type). The filter also 

includes automatic back flushing which removes the larger trapped particles and organisms, 

which, at the same time contributes to the reduction of accumulated sediments in the ballast 

water tanks. 

Apart from pre-filtration, the operational working principles of the OS BWMS include a dual 

combination of cavitation and nitrogen supersaturation. Ballast water is taken on board the ship 

by the use of an existing or additional ballast water pump before being subjected to controlled 

intense pressure pulses arising from hydrodynamic cavitation. In this case, the cavitation is 

generated in a specially developed circumferential cavitation chamber named the C3T unit, 

which operates over a flow rate and pressure difference range with the aid of either active or 

passive back pressure controls (depending on the overall configuration of the ballast water 

system including the ballast water tanks). Harnessed in this way, these pressure pulses are intense 

enough to rupture cell membranes and destroy particles and organisms by forcing them to 

rupture, collapse or collide with one another. In order to achieve desired flow rate capacities, 

identical C3T sub-units are duplicated, arranged in parallel around a circumference, and 

integrated in the actual ballast water pipe in a manner providing identical flow conditions and 

thus identical efficacy for each individual sub-unit. 

Following exposure to cavitation, the ballast water is then supersaturated by the injection of 

nitrogen before it enters the vesselís ballast water tanks. Nitrogen supersaturation causes oxygen 

dissolved in the water to be released, leaving the water in the tanks deficient in oxygen (hypoxic 

condition), thus, severely affecting residual organisms that are dependent on oxygen for their 

survival. The released oxygen and surplus nitrogen is evacuated by the use of conventional tank 

ventilation arrangements. In order to avoid further natural release of the nitrogen over time and to 

prevent potential contamination by outside air entering the ventilation system, a pressure-vacuum 

device is incorporated into the ventilation system to maintain and allow control of optimum 

saturation levels during a voyage. 
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Additionally, in order to ensure compliant efficacy as a function of varying ballast water 

properties, the system also incorporates an isolated (closed circuit - flow through) electrodialytic 

process based on the principles of an electrochemical activation technology, the C2E process. 

The C2E unit applies the principle of electrochemical activation to a small portion of the flow, 

(less than 0.5% by volume) producing a disinfectant which is returned to the main flow after C3T 

(cavitation) exposure and nitrogen injection in order to enhance the overall biological efficacy. 

The C2E unit does this by generating controlled amounts and variations of Active Substances in 

situ without adding any Preparations to the water. A feature of the process is that these activated 

substances naturally degrade over a relative short period of time. Further, the efficacy of the 

disinfectant is enhanced by cavitation since the cavitation causes fragmentation and separation of 

bacterial colonies, etc., which expose organisms previously protected by the surrounding colony 

to the disinfectant, thereby, creating a significant increase in biological efficacy at modest dosage 

and concentration levels. 

The OS BWMS is designed to accommodate: 

.1 existing ships ñ retrofitting; 

.2 new ships ñ integrated design; and 

.3 all capacity ranges. 

The development process has incorporated two prototype ship installations which are used 

actively as research platforms: 

.1 MV Hˆegh Trooper (in operation since June 2005); and 

 .2 MV Federal Welland (in operation since November 2005). 

These installations are, in principle, identical and have been the subject of continuous 

performance assessments for a duration accumulating to more than 40 months. These have 

incorporated: 

- A total of 14 Biological efficacy studies (University of Bergen (UNIFOB)/ GoConsult); 

- Parallel laboratory assessments of corrosion control and coating impact studies in 

compliance with DNVís respective standards (DNV/Safinah Ltd.); 

- Installation studies including vibration analysis (StoGda sp.zo.o Ship Design and 

Engineering (Poland)); 

- A study of the efficacy of filtration under dirty load situations. The initial filtration test 

was undertaken in 2005 at the research facility of NIOZ, the Netherlands (DNV/NIOZ); 

- Testing of a data recording and monitoring system for functionality control of the 

treatment system under the EU CRAFT Programme (OceanSaver Ballast Water 

treatment) (Pole Star Ltd./ Houm as/MAS as/Technological Institute of Norway (TI); and 

- Industrialization ñ Feasibility assessments looking at improvements with focus on 

sampling, system interactions including shipboard automation, installation and 

maintenance issues, etc. For this, the vesselsí crew has been engaged in order to attain 

experience feedback to be used in the process of industrialization. 

Additionally, development work has included land-based laboratory activities with the objective 

of improving the performance of the individual treatment components and enhancing and 

exploiting potential interrelated synergies. Appreciating the initial lack of knowledge in these 

respective areas, the project was forced to put in place its own research facility. A laboratory was 
MEPC 57/2/6 

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established comprising test facilities allowing tests up to 35 m3/hr to be undertaken 

(MetaFil laboratory). The test facility includes 6 simulated ballast water tanks of 1 m3 capacity 

each and a feeding tank of 14 m3; alternatively, the system may also use seawater directly from 

the Oslo fjord. The plant is built in-house and allows all-year operation. Included at the 

laboratory are facilities and workstations for sampling and analysis. 

The resulting designs have been assessed and tested primarily at the MetaFil laboratory at 

Fagerstrand (since May 2005). These assessments include: 

- Principal functional assessments (e.g. confirmation studies on nitrogen 

consumption as a function of gas dispersion methods and oxygen deprivation, 

physical characteristics in the cavitation zone, effects of hydrodynamic imbalance, 

activation of seawater by electrodialysis and insight studies including power 

consumption and biological efficacy, etc., ambient change and associated impacts, 

etc., operational SHE aspects, etc.) (DNV/ MetaFil); 

- Material considerations ñ including erosion studies (MetaFil); 

- Pre-assessment of the impact of hydrodynamic cavitation of the chemical and 

biological properties of ballast water (University of Oldenburg ñ Germany, 

Institute for Chemistry and Biology in the Marine Environment, and Norwegian 

Institute of Water Research ñ NIVA); 

- Simplified and G8 compliant biological efficacy studies at scaled down flow rates: 

 30 ñ 35 m3

 / hr (DNV, NIVA) 

- Toxicity tests (G9 compliant) incorporating all treatment stages (University of Oldenburg 

ñ Germany, NIVA). 

 

1.2 Current Status 

The OS BWMS test unit of 200 m3/hr capacity (operational range: 190 ñ 250 m3/hrs) was 

recently commissioned and G8 compliant testing started in June 2007 at NIVAís facility. 

In parallel, the system, installed on board the car carrier Hˆegh Trooper, has been upgraded to 

include the vessels total ballasting capacity and also including the updated C3T and C2E 

systems. The installed system has a capacity of 2 x 600 m3

/hr. It is expected to be commissioned 

in August 2007 and will be the subject of shipboard testing in accordance with Guidelines (G8), 

immediately after commissioning. 
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2 THE OCEANSAVERÆ BWMS: MAIN COMPONENTS 

2.1 Layout 

The heart of the OS BWMS comprises four main sub-systems which are complemented by an 

additional part described as the control and auxiliary equipment. The four main sub-systems are: 

 .1 Mechanical Filtration Unit; 

 .2 C3T Unit ñ Hydrodynamic cavitation unit; 

 .3 C2E Unit ñ Activated water unit; and 

 .4 Nitrogen (N2) Supersaturation unit. 

The system may be run in different configurations depending on the level of treatment required 

and the particular properties of the ballast water. For example: 

- Filter / C3T / C2E / N2 Supersaturation (or in any alternative sequence); 

- Filter / C2E / N2 Supersaturation (or in any alternative sequence); 

- Filter / C3T / N2 Supersaturation (or in any alternative sequence); and 

- C3T/C2E (or C2E/ C3T). 

In this way, the OS BWMS can be viewed as flexible and modular, and can be applied in 

different configurations for different end user requirements. 

A principal layout of the OS BWMS is detailed in Figure 1 and is described further in the 

following sections. Note that the figure does not present all alternative configurations and 

sequence alternatives as discussed above. 

Figure 1: The OSBWMS: Main Components. Water flow at uptake of Ballast Water. 

Filter, C2E unit and nitrogen supersaturation are not used at discharge. 
MEPC 57/2/6 

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2.2 The mechanical filtration unit 

The primary task of the mechanical filtration unit in the OS BWMS is to prevent larger particles 

and/or organisms from entering the system. This is done, firstly, to protect the treatment plant, in 

particular the C3T unit, and, secondly, to enhance the performance of the remaining treatment 

stages. The mechanical filtration component removes a considerable portion of particles and 

organisms of different size categories depending on the installed mesh size and type. The filter 

used includes an automatic back flushing process which removes trapped residue (particles, 

organisms). Filtration will also reduce the accumulation of sedimentation in ballast tanks. 

Discharge following backflushing takes place only when the filter is in use at the location of 

ballast water uptake. The mechanical filtration unit is developed from existing industrial products 

made from standard marine materials. The mesh standard should be 50 μm or less of either 

wedgewire or weavewire type. 

No Active Substances are produced by the filtration unit. 

2.3 The C3T unit 

The (patent pending) C3T unit in the OS BWMS is a specially designed circumferential 

hydrodynamic cavitation chamber which is able to generate, harness and control intense pressure 

pulses arising from cavitation. In this way, these pressure pulses are intense enough to rupture 

cell membranes and destroy particles and organisms by forcing them to rupture, collapse or 

collide with one another. The use of the cavitation unit produces a mechanical effect on any 

micro-organisms and other living and non-living matter in the water and thus breaks down these 

unwanted elements and, in particular, is able to break down and weaken groups or clumps of 

micro-organisms into smaller-sized colonies (fragmentation). Experience gained through 

land-based experimental testing has shown that this then allows other treatment components in 

the system to act more efficiently. 

The cavitation unit generates cavitation in the water by guiding the water flow into a carefully 

dimensioned circumferential constriction whereby cavitation bubbles are formed. 

This multiphase flow is then directed to a higher pressure outlet where the cavitation bubbles 

implode. Formation and implosion of the cavitation bubbles generates forces and shockwaves 

which affect matter in the water. The design of the geometry is such that these effects occur 

across the whole of the cross-section of the flow whilst being carefully balanced against pressure 

usage and energy loss. Using computational fluid dynamics (CFD) and experimental testing, a 

particular set of dimensions has been found to provide effective cavitation, particularly when 

treating ballast water in order to break down micro-organisms having a size of larger 

than 10μm. It may be noted that this is the target size-range for the device operating under 

shipboard limitations (maximum acceptable pressure loss). Cavitation will also affect 

organism-categories outside the range as described above. 

Literature studies carried out by OceanSaver (Behrends 2006, NIVA 2006) indicated that Active 

Substances from a theoretical point of view could be produced during ballast water treatment by 

hydrodynamic cavitation as a result of formation of free radicals in natural seawater. However, 

no alteration of the chemical and biological properties of the tested seawater was found in a 

follow-up study (Behrends et al, 2007) and the cavitated water did not show any toxic properties 

directly after treatment and after eight days on two different marine organisms, the bacterium 

Vibrio fischeri and the brine shrimp Artemia salina. 
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Our conclusion is, therefore, that no Active Substances are produced in detectable levels by the 

C3T unit. 

Figure 2 illustrates the performance characteristics of the standard C3T sub-unit. 

Figure 2: C3T cavitation characteristics 

2.4 The C2E unit 

2.4.1 Overall description of the unit

The C2E unit (patent pending) incorporated in the OS BWMS consists of three main 

components: the automation and control system; the DC converter/rectifier power supply; and an 

electrodialytic activation cell module ñ in which a flow is separated by means of a 

membrane/diaphragm which allows exposure of the ballast water to a positive or a negative 

charge only at a constant current level. The C2E unit produces electrochemically activated water, 

which when applied in combination with filtration, supersaturation and cavitation, enhances 

overall biological efficacy in particular for the smaller groups of organisms defined in 

the D-2 standard of the Ballast Water Management Convention. The C2E unit does this by 

generating controlled amounts and variations of Active Substances in situ and only in a side 

stream of the main ballast water stream without adding any additional chemicals (Preparations) 

to the water. 

Frequency distribution of the 

imploding cavitation bubbles produced 

by an individual C3T sub-unit. The 

unit generates more than 100,000 

pressure pulses per second. 

Pressure pulse characteristics 

produced by an individual C3T subunit. The unit generates acoustic 

pressure peaks exceeding 10,000 Pa. 
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A side stream of the ballast water is treated in the electrodialytic activation cell and then 

re-injected into the ballast water line. Typically, less than 0.5% by volume of the total water 

flow into the OS BWMS passes through the C2E unit (electrodialytic activation cell(s)). 

The product of the electrodialytic activation cell has the effect of disabling or killing 

micro-organisms, and can also have a beneficial effect on treating organic compounds in the 

water. 

Studies carried out during the development of the OS BWMS have demonstrated that by 

directing only a part of the water through the electrodialytic activation cell and returning a 

product of the electrodialytic activation cell to the water, an effective water treatment is achieved 

without the need to treat the entire water flow. This reduces the amount of electrical power 

required to carry out the water treatment. In addition, the system can be made smaller compared 

to existing water treatment systems due to the comparatively smaller volume of water treated by 

the electrochemical activation cell in order to obtain an overall treatment effect on the whole 

volume of ballast water. 

The portion of the ballast water treated by the electrodialytic activation cell is separated from the 

incoming water flow following filtration and prior to cavitation and then passes through the 

electrodialytic activation cell as the remainder of the water passes by, without being treated by 

the electrodialytic activation cell (illustrated in the schematic presentation in Figure 1). Thus, the 

C2E unit includes a main flow path, whereby the inlet flow path is arranged to separate a portion 

of the flow from the main flow path and direct it through the electrodialytic activation cell. 

Alternatively, the part of the water treated by the electrodialytic activation cell can be provided 

from a separate source, for example an external source of brine or saltwater (or brine/saltwater 

mixed with the bypass from the incoming flow (ballast water)). In both cases, the apparatus may 

include a connection from the outlet of the C2E unit to a main flow path, whereby the product of 

the electrochemical activation cell is added to the main flow path. 

The C2E process is close-circuited and does not require any holding tanks or dosage pumps as it 

utilizes the pressure loss over the C3T unit to drive the take-off and re-injection. There are no 

residual flow or discharge/waste requirements associated to the process. The components used in 

the C2E unit are standard industrial products for shipboard use with the exception of the 

electrodialytic cell which is unique to the OS BWMS. The capacity of the C2E unit is matched in 

a similar way as to that of the C3T unit by applying the concept of modular duplication. 

2.4.2 Electrochemical activation 

The principle of electrochemical activation is applied to treat water in a variety of applications 

including wastewater (e.g. Folsom et al. 1994, Anon. 2006, Prilutsky et al. 2003, Yang et al. 1999, 

Swem et al. 2001, Stroud et al. 2001), swimming pools and potable water. The principal process 

of the C2E unit is that of applying an electric potential difference between two electrodes to the 

water flow separated by a membrane/diaphragm (electrodialytic process). The ion selective 

membrane separates the anolyte and the catholyte flows and allows the concentration of ions 

which result in the formation of metastable ions and free radicals. In conventional electrolysis of 

seawater, most of the complex reactive species formed at the anode and cathode react with each 

other and are largely neutralized immediately, requiring a high level of charge to create 

biological effects. In conventional electrolysis, hypochlorous acid is the dominant stable 

constituent formed. 
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In the C2E process, however, the anolyte solution has higher microbial efficacy than normal 

electrolysis (chlorine based) solutions when compared in terms of measurable active chlorine 

present in solution. As a result, the anolyte has superior sterilizing and disinfectant properties, 

since the reactive species present in the solution are more effective in destroying 

micro-organisms and organic molecules than chlorine alone. 

The catholyte effluent is alkaline (pH ~ 10-12) and the anolyte effluent is acidic (pH ~ 2.4-4). 

The pH in the anolyte may be adjusted by mixing some or all of the catholyte into the effluent. In 

the C2E unit, approximately 50% of the catholyte is mixed with the anolyte resulting in a pH 

around 3 before the side stream is injected into the ballast line. Catholyte is recirculated in the 

cell avoiding waste issues. 

The C2E cell module configuration and application, as described in this document, is patent 

pending. The capacity of the C2E unit is matched similarly to that of the C3T unit by applying 

the concept of modular duplication (including the powering system). 

Item Description 

1 Cathode (-ve Electrode) 

2 Anode (+ve Electrode) 

3 Membrane 

4 Body 

5 Anolyte Production Zone 

6 Catholyte Production 

Zone 

7 Seawater Inlet 

8 Anolyte/Catholyte 

Mixture Outlet 

9 Catholyte Take-Off Valve 

10 Catholyte Outlet 

Figure 3: Operational principle of the C2E 

The ratio between the overall amount of water and the amount of water flowing into and out of 

the electrochemical activation cell is near constant (following any pressure variations in the main 

ballast line), thus, the dosage of the C2E disinfectant by volume is constant. Any necessary 

alterations regarding the concentration of Active Substances in the disinfectant produced over the 

cells are achieved by changing the level of applied electrical current (amperage) and adjusting the 

injection of catholyte. Changes to the necessary settings are indicated by comparing the Oxygen 

Reduction Potential (ORP), Free Available Chlorine levels and pH measured in a calibration 
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loop to measurements taken from a monitoring point downstream of the injection point 

(main ballast line). This is then used as a basis for the adjustments during operation. The ranges 

for desired values of ORP and FAC may be, respectively, 350 ñ 800 mV and 0.05 ñ 2 ppm, 

more preferably, 350 ñ 550 mV and 0.5 ñ 1.5 ppm. When the ORP and/or FAC measured values 

are outside these ranges, then the operation of the electrochemical activation cell is adjusted 

accordingly. 

As the ballast water is stored for a period of time after treatment, this allows for the oxidants and 

reactive Substances from the product of the electrochemical activation cell to have full effect on 

any micro-organisms and other unwanted matter in the water. In the case of ballast water, there 

is generally a reasonable time of storage as the ship moves from port to port before re-loading 

with cargo and discharging the ballast water. This time can be advantageously put to use by 

allowing the product of the electrochemical activation cell to take effect. Experience has verified 

the short duration in which these characteristic values (ORP/ FAC) are elevated. FAC levels are 

typically halved within 6 ñ 8 hours. 

Active Substances and Related Substances will be described in more detail from section 3 and 

following sections. 

2.5 Nitrogen Supersaturation Unit 

In the OS BWMS, a gas injection/mixing unit is provided for the injection of nitrogen (N2) gas 

into the ballast water. Nitrogen may be injected into all or a part of the water flow (typically less 

than 15% of the total water flow) with the main criteria being that the nitrogen is injected in 

sufficient amounts to ensure that the treated water when reaching the ballast tanks is 

supersaturated with nitrogen to a level of around 120-135% supersaturation providing a reduced 

level of dissolved oxygen of 2.5 mg/litre or less. The OS BWMS applies conventional static 

mixers to all gas mixing points. In general, a two-stage dispersion process has proven more 

efficient with respect to gas consumption. Thus, current the configurations apply a two-stage gas 

dispersion principle. 

In the OS BWMS, N2 requirements are met either by on-board production using standard N2 

membrane generators that work by filtering normal air or by shore supply in storage tanks. For 

most vessels, the latter means of supply is considered less practical. N2 is an inert gas, thus N2 

generators are currently found in use on board ships for purposes including controlled 

atmospheres (in reefers), for safety-blanketing on board chemical carriers/LPG-carriers and for 

gas-leakage control on board LNG-carriers. Thus, both the N2 generator as well as the 

compressor are often critical components for the safety of the vessel and are highly evolved for 

shipboard use. It may be noted that an N2 generating unit comprises a compressor and a 

membrane-based unit, allowing nitrogen to be separated from air by resting on the principle that 

different gases will pass through membranes at significantly different rates, thus permitting 

separation. 

The OS BWMS comprises either a storage of pressurized N2 or one or more N2 generating units. 

Operational experience applying such units for supersaturating ballast water in-line on uptake has 

been obtained from the operation of the MV Hˆegh Trooper and MV Federal Welland. 

The units are type approved for shipboard use or subject to a functionality test to be witnessed by 

class. 
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Ballast water is supersaturated by the injection of N2 before it enters the vesselís ballast water 

tanks. Nitrogen supersaturation causes dissolved oxygen to be released, leaving the water in the 

tanks deficient in oxygen (a hypoxic condition), thus, offering as a means of preventing 

re-growth and severely affecting organisms that are dependent on oxygen for their survival. 

The supersaturation of nitrogen also reduces corrosion and the weathering of corrosion protection 

systems such as coatings and paints as oxidation is a cause of such corrosion and weathering. 

This is particularly useful when water is taken into a ballast tank, as otherwise, the oxygen 

naturally present in the ballast water can lead to this failure mode. 

In order to achieve the required level of supersaturation/oxygen deprivation, the capacity 

requirement for nitrogen injection at this purity has been specified at maximum 0.2 kg/m3. 

This relationship is linear and can be scaled up accordingly. 

Nitrogen supersaturation and consequently oxygen deprivation will impact the living conditions 

of organisms present in the treated water. However, the process does not cause any chemical 

reactions or lead to the formation of new chemical compounds. At discharge, the treated water is 

aired to avoid discharge of hypoxic water. It is therefore our conclusion that no Active 

Substances are produced by the application of nitrogen supersaturation when applied as discussed 

in this document. 

2.6 Control and auxiliary equipment 

Several additional elements in the OS BWMS act as control and auxiliary equipment. 

These components can be regarded as standard ìoff-the-shelfî components commonly used in the 

marine industry and as such, do not require much explanation. A summary of the purpose of 

these components is, however, provided as follows: 

Booster Pump

The booster pump caters for the additional pressure requirements of the specific system 

under consideration. The additional pressure requirements supply the driving energy for 

the cavitation process and compensate for additional pressure losses incurred by the 

system that arise through the addition of the mechanical filter, piping system etc. 

For example, the C3T unit has been found to operate within IMO guidelines with an 

upstream pressure immediately in front of the unit between 4 ñ 5 barg. The unit induces a 

pressure loss of approximately 2 ñ 2.5 barg. 

In the case of a retrofit, the booster pump may be an additional standard component that 

is installed in addition to the existing shipís ballast water pump. The sizing of the booster 

pump depends upon the particular system under consideration. Alternatively, one may 

choose to upgrade the delivery pressure from the existing ballast water pump(s) if 

possible, or alternatively change the ballast pump to a pump that meets the overall 

specifications of the OS BWMS. The booster pump is constructed from standard 

materials commonly used in ballast water pumps today and requires similar installation 

and routine maintenance. 

In a new ship, the additional pressure requirements would be taken into account when 

initial sizing and pressure requirements of the new system are carried out. 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

Minimum Pressure Control

The OceanSaverÆ research programme has identified optimum operational parameters for 

the C3T unit including the optimization of implosion pressures, frequency of collapse 

and, consequently, biological efficacy in light of overall considerations including 

shipboard interface issues. The overall efficiency of the unit is greatly improved when the 

back pressure is maintained above a minimum level. However, during filling or empting 

of the ballast water tanks, the system back pressure against which the C3T unit works will 

vary. Therefore, a standard industrial pressure management device may be applied to 

maintain the pressure to the C3T unit within acceptable levels. This device may be 

passive or active (e.g. a constant pressure valve). Note that system backpressure will vary 

according to tank and piping configurations of the specific ship (e.g. pressure build-up 

characteristics of the vessels ballast water tanks during filling) and need to be addressed 

specifically (standard pressure calculations) when specifying the overall ballast water 

system requirements (pipe size, pump capacity, etc.). 

Pressure/Vacuum Valve

The Pressure/Vacuum valve (PVV) is a device designed to maintain pressure and vacuum 

conditions in the individual ballast tank so that pressure exposure does not exceed that of 

its design criteria. Such devices are available ìoff the shelfî for ìdryî operations. In the 

OS BWMS, such valves are applied in order to maintain the N2 blanket over the treated 

ballast water in order to maintain the required level of N2 supersaturation and the 

achieved deficiency of oxygen in the water in the tank. In addition to providing 

protection against underpressurizing/overpressurizing of the ballast tank, they also 

prevent air intake and evaporative losses These pressure vacuum valves maintain a tight 

seal until the tanks overpressure or underpressure exceeds the set minimum or maximum 

pressure threshold values to which the valves are designed. Then the valves allow for 

intake of air or discharge of N2, air or water, until the pressure in the tank is within the 

acceptable range. 

PVV are used in industry in different areas for the purpose of securing pressure safe 

ventilation. The OS BWMS application introduces the presence of water as well as gas 

and, consequently, it has been necessary to develop a valve that manages both. The 

OS PVV has recently undergone considerations by class for certification and is now the 

only type approved PVV available for ìwet atmospheresî in the market. 

Power and Continuous Monitoring

In addition to the components above, there is also an integrated power control system that 

ensures the correct power supply to all components and items at all times. 

Various control sensors and monitoring equipment are installed to measure variables such 

as pump speed and frequency, power, current, voltage, flowrate, pressure, temperature, 

hydrophone data, dissolved oxygen levels, ORP and free residual oxidant. Data from 

these are recorded and used for system control in an integrated system automation loop. 

Appropriate safety features including alarms/warning systems and shut-down procedures 

are also included. The performance of the system may be continuously monitored by use 

of automatic monitoring and data transfer via satellite services such as PurpleFinder. 

This feature has been extensively assessed over the last two years as it has been applied to 

both the vessels included in the research programme. 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

3 ACTIVE SUBSTANCES AND RELEVANT CHEMICALS 

3.1 Definitions 

The component of the OS BWMS deemed relevant for Active Substances approval by this 

application is the C2E unit. In this application, we will use the definitions of ìActive Substanceî, 

ìRelevant Chemicalsî from Procedure for approval of ballast water management systems that 

make use of Active Substances (G9). 

Active Substances are produced in the anode chamber and to some extent in the cathode chamber 

of the C2E unit. However, several of these substances are very short-lived, but may produce 

other chemicals that have effects relevant for Human Exposure Scenario (HES) aspects. 

These reaction products are here defined as Relevant Chemicals together with other possible 

by-products that may be produced by the treatment in the ballast tanks or after discharge. 

The purpose of the nitrogen supersaturation unit is mainly to reduce corrosion in the ballast tanks 

by replacing oxygen by the inert gas nitrogen. Consequently, this is not an Active Substance. 

However, nitrogen supersaturation may have effects on some organisms and may be of concern 

for the safety of the crew. The applicant has defined it as ìOther componentsî and included some 

relevant information for this as well. 

In the following sections, Active Substances and Relevant Chemicals are defined more precisely. 

The following sections will describe the particular chemicals, environmental and safety features, 

discharge characteristics and resulting characteristics of the treated ballast water as required by 

the Draft Methodology of the GESAMP-BWWG. 

3.2 Active Substances 

The electrolytic process in the C2E unit produces an anolyte and a catholyte in separate 

chambers, separated by a diaphragm. The anolyte, which is acidic, is a mixture of short-lived 

oxidative agents, with a documented toxic effect to living organisms. The catholyte, which is 

alkaline, poses a reductive, but limited toxic effect to the organisms. In the C2E unit, 

approximately 50% of the catholyte is circulated into the anode chamber resulting in a pH in the 

Active Substance mixture of around 3 before it is injected into the main ballast line. 

Most literature discussing the products of electrolysis of water 

is concerned with brine solutions (Brine is water saturated or 

nearly saturated with sodium chloride (NaCl)). 

Due to its chemical features (Textbox 1) the electrolysis of 

seawater results in several other compounds compared to 

brine. Alkaline conditions at the cathode electrolysis of 

seawater result in a mineral deposition which precipitates 

calcium and magnesium minerals from seawater: 

OH-

 + HCO3- + Ca2+ = CaCO3 + H2O 

2OH-

 + Mg2+ = Mg(OH)2

Textbox 1: Main components of 

seawater (35 psu) (Wilson 1975): 

 Element mg/L 

 Cl-

 19 354 

 Na+

 10 770 

 Mg2+ 1 290 

 SO4

2- 2 712 

 Ca2+ 412 

 K+

 399 

 Br-

 67 

 HCO3-, CO3

2-, CO2 28 

 Sr2+ 7.9 

 B 4.5 

 F- 1.3 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

Below is listed some of the reactions that form Active Substances found in the literature when 

electrolysing seawater. Due to the large number of possible reactions it is not intended to present 

a complete list, but some of the most relevant for this application are included. 

( )

( )

( )

( )

( )

( )

( )

( )

( )

2 3 ( ) 10

3 6 6 9

4 2 5 8

7

2 2 6

5

4

2 2 3

2

2 2 1

:

2 3 2

2 3

2 2

2 2 2 2

2 2

2 2

2

2 2

2

− −

−

− − −

− −

+

− −

− − − −

− −

+ → + +

→ + +

+ → + +

+ → + +

→ +

• + • →

→ • +

+ → + +

+ → +

→ +

O OH O H O e

H O O e

Cl OH ClO H O e

HClO H O HCl O H O

OH H O e

OH H OH H O

OH OH e

Cl OH ClO H O e

Cl H O HClO HCl

Cl Cl e

Anode reactions

Reaction (1) is the principal anode reaction (White 1999). However, most of the chlorine gas 

reacts rapidly with water and produce hypochlorous acid (2) as the dominant oxidant in the 

anolyte. In seawater, the three species of chlorine (Cl2, HOCl, and OCl-

) are in equilibrium as a 

function of pH, temperature, salinity and other factors. An example of the distribution between 

the two most abundant in coastal water is presented in Figure 4. At a salinity of 32 psu, 

temperature 15oC and pH 8.2, 89% of the chlorine is present as OCl-

 and only 11% as 

hypochlorous acid. The pH in the anolyte from the C2E unit is around 3, which means that nearly 

all chlorine is hypochlorous acid and some as chlorine gas. 

2 2 2 (11)

:

2 2

− − H O + e → H + OH

Cathode reactions
MEPC 57/2/6 

ANNEX 

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Figure 4: The calculated variation in composition of two most abundant components of 

the chlorine equilibrium in seawater (temperature 15oC, salinity 21 psu). 

Common pH range in seawater is marked with a square. 

Reaction (11) is the principal cathode reaction. Hydrogen gas has no environmental effects, but 

has safety concerns. When hydrogen gas is formed, the catholyte become highly alkaline due to 

high concentrations of OH-

. The porous membrane separating the anode and cathode chamber is 

used to inhibit the migration of the OH-

 ions from the cathode to the anode; otherwise, the mixing 

of these solutions would result in the formation of hypochlorite as the dominant oxidant. 

NIVA (2007a) estimated the active compounds formed in the anolyte from the C2E unit 

quantitatively using more or less specific methods of determination. 

Table 1: Active Substances produced by the C2E unit using seawater. Compounds are 

quantified within 2-10 min (NIVA 2007a) 

Test water 

Total

chlorine

mg Cl2/L 

Free 

chlorine 

mg Cl2/L 

Combined 

chlorine 

mg Cl2/L 

Ozone 

mg O3/L 

Hydrogen 

peroxide 

mg H2O2/L 

High salinity 34 psu 1010 980 30 13.7 2.7 

Brackish water 17 psu 870 800 70 5.4 2.1 

Surface water 20 psu 970 930 40 10.9 3.6 

An analysis by Tallinn Technical University (Trapido et al. 1999) of anolyte produced from brine 

in a comparable dialytic cell to the C2E concluded that the anolyte contained the following active 

forms of chlorine: hypochlorous acid (HClO), hypochlorous ion (ClO-

) and chlorine gas (Cl2). 

No presence of chlorite (ClO2

−

) or chlorate (ClO3

−

) ions was found in the anolyte using ion 

chromatography. 

Based on available information, the applicant concluded that the Active Substances formed in the 

C2E unit is primarily hypochlorous acid (HClO) with concentrations of chlorine gas (Cl2), Ozone 

(O3), hydrogen peroxide (H2O2), chlorine dioxide (ClO2) and hypochlorite (ClO-

). 

0,0

0,1

0,2

0,3

0,4

0,5

0,6

0,7

0,8

0,9

1,0

0 1 2 3 4 5 6 7 8 9 10 11 12 13 14

pH

Fraction

HOCl OCl- 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

In relevant databases and literature, there are almost no data on hypochlorous acid (HClO) and 

hypochlorite ion (ClO-

) necessary for the evaluation in the Procedure for approval of ballast 

water management systems that make use of of Active Substances (G9). This is because the 

mixture is not available as a preparation on the market. To compensate, the applicant mainly 

uses data relating to sodium hypochlorite (NaClO) as reference data for the evaluation of the free 

active chlorine in this application. NaClO rapidly hydrolyses in water and resides there as free 

active chlorine. Thus, the HClO and ClO-

 could be evaluated using data on NaClO. 

3.3 Relevant Chemicals 

Apart from the primary anodic and cathodic reactions, there are secondary reactions producing 

Relevant Chemicals, some with documented toxic effect. As these Relevant Chemicals are 

dependent to some part on the quality of the seawater, and the seawater temperature, it is quite 

difficult to give a full estimate of all possible substances that might occur. Chlorination and 

electrolysis of seawater is commonly used as anti-biofouling measure in cooling water circuits in 

European coastal and estuarine power stations. Taylor (2006) and Jenner et al. (1998) reviewed 

the outcome of research on chlorination by-products (CBPs) which can be produced from 

electrolysis of estuarine or seawater and generated through reactions between halogen oxidants 

and organic matter in the water. The following sections are based on these papers together with 

general textbook information on halogen oxidants and seawater chemistry. 

Sugam and Helz (1981) considered 25 different Cl and Br species in chlorinated marine waters 

and found that, for salinities above 3 psu, the following five species would be the important 

contributors to the labile fraction of produced oxidants at pH 6-8: HOBr, OBr-

, NH2Br, NHBr2

and NBr3.

3.3.1 Reaction between Active Substance and bromide ions

All substances produced in both the anolyte and the catholyte are relative short-lived oxidative or 

reductive substances. Owing to the presence of bromine in the seawater (Textbox 1) in excess 

concentrations to the chlorine applied in the OS BWMS, chlorine reacts with the bromide ions to 

form hypobromous acid (Farkas et al. 1988) when the anolyte is injected into the ballast line: 

(12) − − HOCl+ Br → HOBr+Cl

Textbox 2: Chlorine oxidants are described in the literature as ìfreeî, ìactiveî, ìavailableî, ìcombinedî or 

ìresidualî, and by combinations of these adjectives as well (definitions from Jenner et al. 1998, Eidnes & 

Aareskjold 1992, NIVA 2007a) 

1. Free oxidant/Free available oxidant in seawater is present mainly as an equilibrium mixture of hypochlorous 

acid, hypochlorite ions, hypobromous acid and hypobromite ion. 

2. Combined oxidant/Combined available oxidant is available as bromamines, chloramines or other 

compounds having an N-C link. These are also oxidants but less effective than the free oxidants. 

3. Total available oxidant/Total free oxidant is the sum of (1) and (2). 

4. Total residual oxidant (TRO) is identical to (3), but emphasise the concept of pool of oxy-disinfectant 

capacity that persists after the initial demand (see below) has been met. 

5. Oxidant initial demand is defined as the difference between the amount of oxidant added and the useful 

(residual) oxidant (TRO) remaining at the end of a specified contact period. 

6. Oxidant decay is a continuing serie of reactions that will in time lead to a complete disappearance of all 

measurable oxidant. 
MEPC 57/2/6 

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The reaction rate between chlorine and bromide ion is rapid. With assumed seawater conditions 

(35 psu, 25oC, pH 8.3), Selleck et al. (1976) calculated the time required to convert 99% of the 

chlorine to bromine to be around 10 seconds. 

Similar to hypoclorous acid, hypobromous acid (HOBr) will dissociate depending upon pH, 

temperature and salinity. However, at pH 8 and normal salinities and temperatures for seawater, 

the un b dissociated HOBr can be calculated to approximately 83% versus HOCl at only 28%. 

Consequently, the presence of bromine increases the biological efficacy of the OS BWMS. 

3.3.2 Reaction between Active Substance and nitrogen compounds 

Inorganic nitrogen (ammonia, nitrite and nitrate) and organic nitrogen (amino acids, proteins) 

reside in natural seawater as nitrogen compounds. Some of the hypochlorous acid and hypobromous 

acid react with these nitrogen compounds and form N-chloro or N-bromo compounds, commonly 

called halogenamines. There are two distinct classes ñ organic and inorganic. 

If water contains ammonia nitrogen, inorganic chloro- and bromamines will be formed rapidly 

(e.g. NH2Br, NHBr2 and NHBr3). Changing the pH value, influences the amount of mono-, diand tribromamine that is formed. According to reaction rates established by Morris (1952, 1965) 

(cited in White 1999), the fastest conversion of HOCl to NH2Cl occurs at pH 8.3 which is the 

normal pH of seawater. The reaction slows appreciable as temperature drops. Dichloramine and 

trichloramine will form at pH around 8 if excess chlorine is available (White 1999). 

All halogenamines are included in the measured total available oxidant or total residual oxidant 

(TRO) (Textbox 2). 

3.3.3 Reaction between Active Substance and organic compounds 

Other Relevant Chemicals are so-called Disinfection By-Products (DBPs) that are both organic 

and inorganic substances formed when Active Substances react with naturally occurring 

compounds in the water. DBPs are normally formed in reactions where organic chemicals play a 

major part. 

A relatively limited number of studies appear to have focused on DBP formation in marine 

waters. Most of the studies have analysed chlorinated cooling water samples from coastal and 

estuarine power stations. Some of the most relevant studies have been summarized in Table 2 

together with results from direct measurements on samples collected during an initial full-scale 

testing of the OS BWMS. 
MEPC 57/2/6 

ANNEX 

Page 20 

I:\MEPC\57\2-6.doc 

Table 2: Summary of results from relevant studies on chlorination of marine waters. 

Results from direct measurements on samples collected during a preliminaryfull-scale 

testing of the OS BWMS at Solbergstrand summer 2007 are also shown (- = not analysed). 

 OceanSaver© Taylor 

(2006) 

Allonier et al. 

(1999) 

Fabbricino & 

Korshin 

(2005) 

 Contr. 

Test 

day 

0 

Test 

day 

5 

Before After

0.2-0.8 

mg 

Cl2/l 

5 mg 

Cl2/l 

Coastal 

water 

1 mg 

Cl2/l 

Deep 

water 

1 mg 

Cl2/l 

Chemical Name μg/l μg/l μg/l μg/l μg/l μg/l μg/l μg/l μg/l 

AOX 29 386 1290 

EOX <50 <50 <50 0.3-2.4 1-13 

2-

monochlorophenol <0.1 <0.1 <0.1 

3- 

monochlorophenol <0.1 <0.1 <0.1 

4- 

monochlorophenol <0.1 <0.1 <0.1 

2,3-dichlorophenol <0.1 <0.1 <0.1 

2,4+2,5-

dichlorophenol <0.2 <0.2 <0.2 <0.4 <0.4 

2,6-dichlorophenol <0.1 <0.1 <0.1 

3,4-dichlorophenol <0.1 <0.1 <0.1 

3,5-dichlorophenol <0.1 <0.1 <0.1 

2,3,4-

trichlorophenol <0.1 <0.1 <0.1 

2,3,5-

trichlorophenol <0.1 <0.1 <0.1 

2,3,6-

trichlorophenol <0.1 <0.1 <0.1 

2,4,5-

trichlorophenol <0.1 <0.1 <0.1 

2,4,6-

trichlorophenol <0.1 <0.1 <0.1 <0.06 <0.06 

3,4,5-

trichlorophenol <0.1 <0.1 <0.1 

2,3,4,5-

tetrachlorophenol <0.1 <0.1 <0.1 

2,3,4,6-

tetrachlorophenol <0.1 <0.1 <0.1 

2,3,5,6-

tetrachlorophenol <0.1 <0.1 <0.1 

pentachlorophenol <0.1 <0.1 <0.1 

trichloromethane/ 

chloroform <0.3 <0.3 <0.3 <0.1 <0.1-0.3 <2 ca 0.2 ca 0.2 

tribromomethane/ 

bromoform <0.1 385 398 <0.1-1.0 1-43 7-27 130-170 ca 105 ca 10 
MEPC 57/2/6 

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Dibromochloromethane <0.1 14.7 17.8 <0.1 0.1-

2.2 5-10 ca 3 ca 0.3 

Dichlorobromomethane <0.1 0.297 0.337 <0.1 0.1-

1.0 <1 ca 0.2 < 0.1 

Monochloroacetic 

acid - - - <1 <1 <1 ca 1 

Dichloroacetic acid - - - <1 <1 <1 ca 1 

Trichloroacteic 

acid - - - <1 <1 <1 ca 7 

Monobromoacetic 

acid - - - <1 <1-5 2-3 ca 2 <1 

Dibromoacetic 

acid - - - <2 <2-10 

7.3-

10.2 

11-

28 ca 16 ca 3 

Tribromoacetic 

acid - - - ca 75 n/a 

Bromochloroacetic 

acid - - - <1 n/a 

Dibromochloroacet

ic acid - - - 3-4 ca 1 n/a 

Bromodichloroacet

ic acid - - - <1 ca 3 

Monobromoacetonitrile - - - 0-5 

Dibromoacetonitril

e 

- - - <0.1 0.1-

5.0 0.9-3.6 ca 23 ca 3.8 n/a 

Bromochloroacetonitrile - - - ca 0.1 ca 0.02 

2,4-dibromophenol - - - <0.02 <0.0

2 

2,6-dibromophenol - - - <0.1 <0.1 

2,4,6-

tribromophenol - - - <0.05 <0.0

5-0.3 

0.1-

0.37 1.6 

Dibromoethane - - - 0.1 0.7 

1,2,3-

trichloropropane - - - 0.2 15.8 

2-chlorotoluene - - - 0.1 2.2 

4-chlorotoluene - - - 0.1 1.3 

1,2-dibromo-3-

chloropropane - - - <0.1 1.2 

1,2,3-

tribromobenzene - - - <0.1 1.1 

In this initial test of the OS BWMS, the chlorine concentrations used were higher (3-4 mg/L) 

than normal operation (1.5 ñ 2.5 mg/L). Further analyses of samples taken during the full-scale 

test, with normal concentrations of chlorine, will include chemicals found by Taylor (2006) 

(see Table 2). 

From the literature review and preliminary analyses, the main Relevant Chemicals have been 

selected and shown in Table 3. 
MEPC 57/2/6 

ANNEX 

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Table 3: Main Relevant Chemicals expected to be produced using the C2E unit 

Chemical Name Empirical formula 

trichloromethane/chloroform CHCl3

tribromomethane/bromoform CHBr3

Dibromochloromethane CHBr2Cl 

Dichlorobromomethane CHBrCl2

Trichloroacetic acid C2HCl3O2

Monobromoacetic acid C2H3BrO2

Dibromoacetic acid C2H2Br2O2

Tribromoacetic acid C2HBr3O2

Dibromochloroacetic acid C2HBr2ClO2

Bromodichloroacetic acid C2HBrCl2O2

Monobromoacetonitrile C2H2BrN 

Dibromoacetonitrile C2HBr2N 

2,4,6-tribromophenol C6H3Br3O 

Dibromoethane C2H4Br2

1,2,3-trichloropropane C3H5Cl3

2-chlorotoluene C7H7Cl 

4-chlorotoluene C7H7Cl 

1,2-dibromo-3-chloropropane C3H5Br2Cl 

1,2,3-tribromobenzene C6H3Br3

3.4 Other chemicals 

Nitrogen (N2) is the most abundant gas in the atmosphere and in the ocean (Table 4). It is not 

used directly by living organisms except for certain bacteria and concentrations in the water 

column are, therefore, driven by physical processes. 

Table 4: The percentage by volume of gases in the atmosphere and in seawater 

Gas 

Percentage by 

volume in 

atmosphere 

Percentage by 

volume in surface 

seawater1 

Nitrogen (N2) 78.03 48 

Oxygen (O2) 20.99 36 

Carbon dioxide (CO2) 0.03 15 

Argon, Helium, Neon, etc. 

(Ar, He, Ne) 0.95 1 

totals 100 100 

1 Salinity = 36 psu, Temperature 20oC 

The solubility of gases in water varies with temperature and salinity. In natural seawater, the 

supersaturation of inert gases, such as nitrogen, is primarily controlled by diffusive and 

bubble-mediated air-sea gas exchange as well as by temperature change and atmospheric 

pressure. Observations from coastal waters show that bubbles can be transported to a depth of 

two to three times the prevailing wave height, thus enhancing gas transfer into the water by way 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

of hydrostatic pressure (Atkinson 1973). Supersaturation of natural seawater with oxygen 

at 130% and nitrogen at 120% of air saturation are measured. 

There are several reports of fish mortality from natural water supersaturated with nitrogen 

including sea trout, large scale menhaden (Brevoortia patronus), bay anchovies (Anchoa 

mitchilli), Atlantic croakers (Micropogon undulatus), eels (Myrophis punctatus), and longnose 

gar (Lepisosteus osseus) (Renfro 1963, Baath et al. 1989, Machado 1989). Gas bubble disease 

was identified as the cause of death. Increased mortality caused by IPN virus in rainbow trout has 

been observed from as low as 103% supersaturation after long time exposure (weeks ñ months) 

and gas bubble disease has been observed after 60 days exposure at 5% supersaturation. 

There are, however, few, if any, observations of effects after short time exposure (hours ñ days) 

by less than 110% supersaturation (Jensen et al. 1986). 

The biological effects of supersaturation in natural waters are much smaller than in laboratory 

experiments (Heggberget 1984) probably because fish and other mobile organisms may avoid 

supersaturated water (Stickney 1968). 

Three experiments have been identified testing nitrogen (air) supersaturation as a possible ballast 

water treatment technology: 

- Tamburri et al. (2001) testing deoxygenation of ballast water by nitrogen 

supersaturation and effects on juveniles of three species (polychaet Ficopomatus 

enigmaticus, zebra mussel Dreissena polymorpha, and green crab Carcinus 

maenas). 

- Jelmert (2001) testing effects of air supersaturated water on two species (brine 

shrimp Artemia sp. and juveniles of the common mollusc Mytilus edulis). 

- Dragsund et al. (2002) testing biological efficacy of nitrogen supersaturation in a 

small scale (< 3m3

/hr) ballast water treatment test facility. 

Nitrogen gas is an inert, non-toxic and non-bioaccumulating element. The biological effects of 

nitrogen supersaturation are mainly due to deoxygenation of the water. In the following text, the 

nitrogen supersaturation unit is therefore only discussed in relation to safety aspects regarding 

ambient air quality in the engine room and ballast tanks. 
MEPC 57/2/6 

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I:\MEPC\57\2-6.doc 

4 DATA SET FOR ACTIVE SUBSTANCES AND RELEVANT CHEMICALS 

4.1 Overview of Active Substances and Relevant Chemicals 

4.1.1 Active Substances 

Component 

Chemical Name 

CAS 

Number 

UN 

Number 

Molecular 

Weight (g/mol) 

Empirical 

formula 

Hypochlorous acid 7790-92-3 n/a 52.460 HOCl 

Hydrogen peroxide 7722-84-1 2015 34.015 H2O2

Ozone 10028-15-6 47.998 O3

Chlorine dioxide 10049-04-4 9191 69.5 ClO2

4.1.2 Relevant Chemicals 

Component Chemical 

Name 

CAS 

Number 

UN 

Number 

Molecular 

Weight (g/mol) 

Empirical 

formula 

Bromoform 75-25-2 2515 252.731 CHBr3

Dibromochloromethane 124-48-1 2810 208.290 CHBr2Cl 

Dichlorobromomethane 75-27-4 8027 163.83 CHBrCl2

2, 4, 6 - 

Tribromophenol 

118-79-6 2811 330.82 C6H3Br3O 

Dibromoacetonitrile 3252-43-

5 

2810 198.86 C2HBr2N 

Monobromoacetic acid 79-08-3 1938 138.94802 C2H3BrO2

4.1.3 Other chemicals 

Component 

Chemical Name 

CAS 

Number 

UN 

Number 

Molecular 

Weight (g/mol) 

Empirical 

formula 

Nitrogen gas 7727-37-9 1066 28.013 N2

4.1.4 Structural formula 

Hypochlorous 

acid 

Hydrogen 

peroxide 

Ozone Chlorine 

dioxide 

Bromoform Dibromo 

chloromethane 

Dichlorobromomethane 2, 4, 6 ñ 

Tribromophenol 

Dibromo 

acetonitrile 

Monobromoacetic 

acid 

Nitrogen 

gas 

 
MEPC 57/2/6 

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I:\MEPC\57\2-6.doc 

4.2 Physical and chemical properties for the Actives Substances and Preparations and 

treated ballast water 

Available data describing the properties of the chemicals is highly variable and when sufficient 

data have not been obtainable, the chemical is not presented. 

4.2.1 Active Substances 

Property Hypochlorous 

acid 

Sodium 

hypochlorite 

Hydrogen 

peroxide 

Ozone Chlorine 

dioxide 

Melting point ( ̊C) - -25 -33 

35% w/w in 

water 

-526.5 

-59 

Boiling point ( ̊C) - 107 108 at 1013 hPa 

35% w/w in 

water 

-112o

C 

11 

Flash point ( ̊C) - N/A 

Density kg/m3 at 20 ̊C - 

1.21g/cm3 

1.1-1.2 

35% w/w in 

water 

2.144g/L 

(0o

C) 

1.01g/cm3

(4o

C) 

Vapour pressure at 

20 ̊C 

- 17.4-20 hPa 0.48 hPa at 

30°C 

41257 mm 

Hg (-12 oC) 

1420 hPa 

Vapour density (air = 1) - - - - 2,3 

Water solubility (g/L) Soluble 293 100% 

miscibility at 

any ratio 

 7.5 g/L 

pH in solution - - - - 2-3 (8g/L) 

Dissociation constant 

(pKa) 

7.5 - - - - 

Octanol/water 

partition coefficient 

(log Kow) 

-0.87 -3.42 -0.296 - - 

Corrosivity to 

material or 

equipment 

- - Reacts with 

rust, brass, zinc, 

nickel, copper, 

iron and their 

alloys 

- - 

Explosive properties - - Vapor in 

equilibrium 

with aqueous 

solutions above 

70% by weight 

can explode 

- Explosive 

with or 

without 

contact 

with air 

Oxidizing properties - One of the 

more 

commonly 

used 

oxidizing 

agent 

Classified as 

oxidizing agent 

for transport 

- Strong 

oxidizing 

agent 
MEPC 57/2/6 

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I:\MEPC\57\2-6.doc 

4.2.2 Relevant Chemicals 

Property Bromo 

form 

Dibromochlor

omethane 

Bromodichlor

o-methane 

 2,4,6 - 

Tribromoph

enol 

Dibromo 

acetonitrile 

Bromo 

acetic 

acid 

Melting point ( ̊C) 8.0-8.5 -20 -55 93 67 49 

Boiling point ( ̊C) 149.5 119-120 87 at 

760 mm Hg 

290 at 

994,58 hPa 

67 at 24.0 

mm Hg 206 

Flammability ( ̊C) N/A - - nonflammable. 

>93 - 

Density 2.89 - - 2.55 - - 

Vapour pressure at 

20 ̊C 667 5.54 mm Hg 50.0 mm Hg - 

2.0 mm Hg 

at 50°C ; 15 

mm Hg 

at 70°C; 48 

mm Hg 

at 95°C 

- 

Vapour density 

(air = 1) 

8.72 

(calculate

d) 

2.451 - - - - 

Water solubility Slight 0.4 g/100 mL 5-10 mg/mL 

at 19°C 

50 mg/mL 

at 20 °C 

5-10 

mg/mL 

at 21.5°C 

miscible 

Octanol/water 

partition coefficient 

(log Kow) 

0.38 2,08 1,88 4,02 N/A 0.295 

Dissociation 

constant pKa 2.06 2.16 - - - - 

Corrosivity to 

material or 

equipment 

Not 

corrosive - - - - - 
MEPC 57/2/6 

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I:\MEPC\57\2-6.doc 

4.3 Data on environmental fate and effects under aerobic and anaerobic conditions 

4.3.1 Modes of degradation 

4.3.1.1 Bromoform 

In air, brominated trihalomethanes (THMs) may be degraded by photo-oxidative interaction with 

atmospheric hydroxyl radicals; their typical atmospheric half-life is about 2 months. 

The main route of loss of THMs from the water phase has been reported to be through 

volatilization, with a recorded volatilization half-life ranging from 0.5 hours to 24 days. 

(WHO 1996, Taylor 2006). The reported biodegradation half-life under aerobic conditions has 

been reported to around 1 month (Taylor, 2006). Under anaerobic conditions, brominated 

trihalomethanes are readily bio-degraded within days in the presence of methane-producing 

bacteria and under denitrifying and sulphate-reducing conditions (Taylor, 1996). Adsorption to 

suspended matter and abiotic degradation (e.g. via hydrolysis) have been reported as negligible 

(Taylor, 2006); The estimated half-life through hydrolysis in aqueous media is 686 years for 

bromoform (WHO, 1996). 

During experiments in open (air exposed), reaction vessels (150 litres) concentrations of THMs 

in chlorinated seawater decreased from 15 lg/L to <0.25 lg/L over 7 days. (In closed reaction 

vessels, only a small decrease of THMs in chlorinated water was observed .) The following first 

order rate constant (k) and half-life (t0.5) were determined for Bromoform: total loss: k = 0.027, 

h_1 t0.5 = 26 h; net volatilization loss: k = 0.024, h_1 t0.5 = 28 h. 

The potential toxicity (pT) of open vessels of chlorinated seawater declined to non-chlorinated 

intake levels within 2 ñ 3 days. Thereafter, the pT remained relatively constant. In a closed 

system, no significant decrease in pT was observed. Although samples were tested for 

genotoxicity, the results were equivocal ñ local inputs, probably from other industrial activities, 

were sufficient to mask any influence of low-level chlorination (Taylor 2006) 

Bromoform should be regarded relatively persistent once released into the environment 

(also stated in GESAMP-BWWG 3/9 (MEPC 56/2/2)). 

4.3.1.2 Dibromochloromethane 

(As for Bromoform; THMs in general.) 

 

In Taylor (2006), the following first order rate constant (k) and half-live (t0.5) were determined 

for DBCM (in seawater): total loss: k = 0.040, h_1 t0.5 = 17 h; net volatilization loss: k = 0.031, 

h_1 t0.5 = 22 h. 

Adsorption to suspended matter and abiotic degradation (e.g. via hydrolysis) has been reported as 

negligible (Taylor, 2006); estimated half-live through hydrolysis in aqueous media is 274 years 

for DBCM (WHO, 1996) (see also MEPC 56/2), thus DBCM should be regarded relatively 

persistent once released into the environment. 
MEPC 57/2/6 

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I:\MEPC\57\2-6.doc 

4.3.1.3 Dichlorobromomethane 

(As for Bromoform; THMs in general.) 

In Taylor (2006), the following first order rate constant (k) and half-life (t0.5) were determined 

for DCBM (in seawater): total loss: k = 0.080 h_1 t0.5 = 9 h. 

Adsorption to suspended matter and abiotic degradation (e.g. via hydrolysis) has been reported as 

negligible (Taylor, 2006); estimated half-life through hydrolysis in aqueous media is 1000 years 

for DCBM (WHO, 1996), thus DCBM should be regarded relatively persistent once released into 

the environment. 

4.3.1.4 Tribromophenol 

Halophenols have been known to be partially ionised at ambient pH values. The volatilization 

half-lifes of 2,4-dichlorophenol and 2,4,6-trichlorophenol have been reported as 2 weeks. 

Halophenols have been known to be susceptible to photodegradation and this has been 

understood to be the major fate process, with a half-life of several days (Taylor, 2006). 

Volatilization of non-dissociated 2,4,6-TBP from water surfaces is not expected to be an 

important fate process (Danske Milj ̄ministeriet, 2000). 

Tribromophenol is not regarded as readily biodegradable (49% of BOD, 4w, 100 mg/L 

substance, 30 mg/L sludge) (Danske Milj ̄ministeriet, 2000), however, adapted communities of 

micro-organisms and specialist communities (such as anaerobic or sulfidogenic) may degrade the 

compounds (WHO 2005). Biodegradation half-lifes have been reported as being 7 days and the 

degree of adsorption to suspended solids and sediments (and bioconcentration) has been reported 

as moderate (Taylor, 2006, WHO 2005). 

4.3.1.5 Dibromoacetonitrile 

The half-lifes of dihaloacetonitriles such as dibromoacetonitrile (DBAN) have been reported as 

being of the order of several days, dependent on pH, with the primary route being gradual 

hydrolysis into dihalolacetic acids. Adsorption to solids has been reported as negligible 

(Taylor, 2006). 

In Taylor (2006) for both open and closed reaction vessels (seawater), >90% dibromoacetonitrile 

was lost in 40 h giving k = 0.050, h_1 t0.5 = 14 h. The potential toxicity (pT) of open vessels of 

chlorinated seawater declined to non-chlorinated intake levels within 2ñ3 days. Thereafter the pT 

remained relatively constant. In a closed system no significant decrease in pT was observed. 

Although samples were tested for genotoxicity the results were equivocal: local inputs, probably 

from other industrial activities, were sufficient to mask any influence of low-level chlorination 

(Taylor, 2006). 
MEPC 57/2/6 

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I:\MEPC\57\2-6.doc 

4.3.2 Bioaccumulation, partition coefficient, octanol/water partition coefficient 

4.3.2.1 Hypochlorous acid 

 Results 

Log Kow -0.87 hypochlorous acid 

-3.42 sodium hypochlorite 

Koc 14.3 hypochlorous acid 

14.3 sodium hypochlorite 

1⁄2-life 0.8 h hypochlorous acid 

1.4 h sodium hypochlorite 

Hypochlorous acid and sodium hypochlorite can not be considered as bioaccumulative based on 

given data. 

As the log Kow values for sodium hypochlorite and hypochlorous acid are very low, it is 

considered unlikely that these substances should accumulate through the food chain. 

4.3.2.2 Hydrogen peroxide 

Results Reference 

Log Kow H2O2 does not accumulate in cells of living 

organisms 

 IUCLID 2000 

4.3.2.3 Bromoform 

Bromoform may be slightly bioconcentrated by aquatic organisms, though the octanol/water 

partition coefficient (Kow) is 2.38, which is smaller than the rough indication value for 

bioaccumulation potential of Log Kow > 3). The chemical may in case of bioaccumulation tend 

to partition to fat tissues of aquatic organisms (WHO, 1996). 

As described in Taylor (2006) for coastal and estuarine power stationís cooling water, the 

influence of long-term exposure by chlorination residues (including bromoform) on sea bass 

(Dicentrarchus labrax) was found to be very limited. Although some bioaccumulation of 

bromoform was noted during annual chlorination seasons, this accumulation rapidly dissipated 

thereafter. No impacts on growth were observed and no damage to liver tissues was observed. 

4.3.2.4 Dibromochloromethane 

DBCM may be faintly bioconcentrated by aquatic organisms, although the octanol/water 

partition coefficient (Kow) is 2.08, which is smaller than the rough indication value for 

bioaccumulation potential of Log Kow > 3. The chemical may in case of bioaccumulation tend to 

partition to fat tissues of aquatic organisms (WHO, 1996). 

As described in Taylor (2006) for coastal and estuarine power stationís cooling water, the 

influence of long-term exposure by chlorination residues (including bromoform) on sea bass 

(Dicentrarchus labrax) was found to be very limited. Although some bromoform 

bioaccumulation was noted during annual chlorination seasons, this accumulation rapidly 

dissipated thereafter. No impacts on growth were observed and no damage to liver tissues. 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

4.3.2.5 Dichlorobromomethane 

DCBM may be faintly bioconcentrated by aquatic organisms, although the octanol/water 

partition coefficient (Kow) is 1.88, which is well below the rough indication value for 

bioaccumulation potential of Log Kow > 3. It is suggested that the chemical in case of 

bioaccumulation will tend to partition to fat tissues of aquatic organisms (WHO, 1996). 

As described in Taylor (2006) for coastal and estuarine power stationís cooling water, the 

influence of long-term exposure by chlorination residues (including bromoform) on sea bass 

(Dicentrarchus labrax) was found to be very limited. Although some bromoform 

bioaccumulation was noted during annual chlorination seasons, this accumulation rapidly 

dissipated thereafter. No impacts on growth were observed and no damage to liver tissues. 

4.3.2.6 2,4,6-Tribromophenol 

Measured values suggest that the potential for bioconcentration of 2,4,6-TBP in aquatic 

organisms is moderate to high. Octanol/water partition coefficient (log Kow) is 4.02. 

Exposure of bluegills (Lepomis macrochirus) to 14C-labelled 2,4,6- TBP for 28 days resulted 

in 20-fold bioaccumulation in edible tissue and 140-fold bioconcentration in viscera. Plateau 

levels were reached by 3 ñ 7 days of exposure. The half-life for residues was less than 24 h 

following termination of exposure (WHO 2005). 

As described in Taylor (2006) for coastal and estuarine power stations cooling water, the 

influence of long-term exposure by chlorination residues (including 2,4,6-Tribromophenol) on 

sea bass (Dicentrarchus labrax) was found to be very limited. Although some bromoform 

bioaccumulation was noted during annual chlorination seasons, this accumulation rapidly 

dissipated thereafter. No impacts on growth were observed and no damage to liver tissues. 

4.3.2.7 Dibromoacetonitrile 

Adsorption to sediment and bioconcentration in aquatic organisms is stated in WHO (2004) as 

ìnot expectedî. 

As described in Taylor (2006) for coastal and estuarine power stations cooling water, the 

influence of long-term exposure by chlorination residues (including Dibromoacetonitrile) on sea 

bass (Dicentrarchus labrax) was found to be very limited. Although some bromoform 

bioaccumulation was noted during annual chlorination seasons, this accumulation rapidly 

dissipated thereafter. No impacts on growth were observed and no damage to liver tissues. 

4.3.3 Persistence and identification of the main metabolites in the relevant media 

(ballast water, marine and fresh waters) 

4.3.3.1 Bromoform 

BDCM is metabolized to phosgene, whereas DBCM and bromoform are metabolized to 

brominated analogues of phosgene. The rate of metabolism of these compounds to carbon 

monoxide both in vivo and in vitro generally follows the halide order: namely, bromoform >> 

DBCM > BDCM >> chloroform. IPCS (2000) postulated that the brominated THMs may be 

more rapidly and more extensively metabolized than their chlorinated counterparts. Although this 
MEPC 57/2/6 

ANNEX 

Page 31 

I:\MEPC\57\2-6.doc 

may be true for BDCM, support for this statement, as it pertains to DBCM or bromoform, is 

difficult to determine from the limited literature currently available. The majority of the 

comparative metabolism studies conducted to date are limited to chloroform or BDCM. 

Nonetheless, it would appear that the toxicity of BDCM and likely other brominated THMs is 

mediated through a bioactivation pathway (from WHO 2005). 

No information on persistence of metabolites has been found. 

4.3.3.2 Dibromochloromethane 

See description for bromoform. 

According to MEPC 56/2, no persistent substance is formed. 

4.3.3.3 Dichlorobromomethane 

See description for bromoform. 

No information on persistence of metabolites has been found. 

4.3.3.4 2,4,6-Tribromophenol 

TBP is in itself a natural metabolite from infauna in marine pristine soft bottom habitats 

(for example from Acorn worms (enteropneusta)). However, no information was found on the 

metabolites of TBP (same conclusion in WHO 2005). 

4.3.3.5 Dibromoacetonitrile 

Halogenated acetonitriles are metabolized via oxidative dehalogenation and dehydration to 

carbon dioxide and cyanide, which is then further metabolized to thiocyanate. The first step in 

this reaction is catalysed by a mixed-function oxidase (such as a cytochrome P-450) and results 

in production of a halocyanomethanol. It is proposed that the halocyanomethanols then dehydrate 

to form halocyanoformaldehydes or lose cyanide to form haloformaldehydes, including 

phosgene. The cyanide carbon group is more readily excreted in the urine, whereas the 

halomethyl carbon group is excreted nearly equally in expired air and in urine; excretion in 

faeces is low (WHO 2004). 

Data on persistence of main metabolites have not been found. 

4.3.4 Reaction with organic matter 

4.3.4.1 Bromoform

When chlorine or bromine is used to treat ballast water, trihalomethanes such as bromoform are 

formed as a by-product. They result from the reaction of chlorine and/or bromine with organic 

matter in the water being treated. However, once the bromoform is formed, it does not appear to 

have any further reactions with organic matter (MEPC 56/2/3). 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

4.3.4.2 Dibromochloromethane 

When chlorine or bromine is used to treat ballast water, THMs are formed as a by-product. They 

result from the reaction of chlorine and/or bromine with organic matter in the water being treated. 

However, once the THM is formed it does not appear to have any further reactions with organic 

matter. 

4.3.4.3 Dichlorobromomethane 

When chlorine or bromine is used to treat ballast water, THMs are formed as a by-product. They 

result from the reaction of chlorine and/or bromine with organic matter in the water being treated. 

However, once the THM is formed, it does not appear to have any further reactions with organic 

matter. 

4.3.4.4 2,4,6-Tribromophenol 

Bromophenols can be formed during the chlorination of natural water and wastewater containing 

phenol and bromide ions. No information has been found on further reactions with organic 

matter. 

4.3.5 Potential physical effects on wildlife and benthic habitats 

4.3.5.1 Bromoform 

No information is available on the effects on wildlife or benthic habitats (MEPC 56/2/3), 

however, significant physical effects have not been considered relevant for this substance. 

4.3.5.2 Dibromochloromethane 

DBCM has a higher specific gravity than seawater (2.451 (20°C)) and a low solubility (2.7g/L (20°C)). 

Therefore, according to evaluation based on GESAMP hazard evaluation (GESAMP (2002)), the 

compound is classified as Rating S (substances having a potential effect on benthic habitats) 

(MEPC 56/2). 

4.3.5.3 Dichlorobromomethane 

No information has been available on physical effects on wildlife and benthic habitats, however, 

significant physical effects have not been considered relevant for this substance. 

4.3.5.4 2,4,6-Tribromophenol 

No information has been available on physical effects on wildlife and benthic habitats, however, 

significant physical effects have not been considered relevant for this substance. 

4.3.6 Potential residues in seafood 

4.3.6.1 Bromoform 

No information has been found on bromoform residues in seafood (see also MEPC 56/2/3). 
MEPC 57/2/6 

ANNEX 

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I:\MEPC\57\2-6.doc 

4.3.6.2 Dibromochloromethane 

As DBCM is considered to have low bioaccumulation potential, its persistence in seafood is 

expected to be low. According to studies, DBCM was not detected in oysters, clam and the 

sediment of the Ariho River and the Yoshinaga River (MEPC 56/2). 

4.3.6.3 Dichlorobromomethane 

DBCM is not a common food contaminant but has been found in trace amounts in some 

samples: 1.2 μg/kg in one dairy composite and 7 μg/kg in butter (WHO, 1996). However, 

information on potential residues in seafood has not been found. 

4.3.6.4 2,4,6-Tribromophenol 

2, 4, 6-tribromophenol has been measured in wild-harvested prawns and ocean fish in Eastern 

Australia. The levels ranged from 0.1 to 230 ng/g in fish (gut, flesh) and 0.12-460 ng/g in prawns 

(head, tail) (Danske Milj ̄ministeriet, 2000). In biota likely to form part of human diets, edible 

portions contain mean 2,4,6-TBP concentrations up to 198 and 2360 μg/kg dry weight in 

molluscs and crustaceans, respectively, and up to 39 μg/kg dry weight in marine fish. Brominated 

phenols have been detected in human milk, blood, and adipose tissue (WHO 2005). 

4.3.7 Interactive effects 

No information has been found on interactive effects. 

4.4 Effects on aquatic plants, invertebrates, fish and other biota 

The Active Substances are added to eliminate organisms present after the initial physical 

treatment (i. e. filtration) of the ballast water. However, when added to the ballast-water, new 

compounds might be formed in reaction with the Active Substances. The toxicity of these 

compounds is of importance to the crew on the ship and to the environment where the ballast 

water is expelled. The toxicity of an Active Substance is not definite; it acts differently on 

different organisms, resulting in a variety of LC50 (Lethal Concentration for 50%), EC50

(Effective Concentration for 50%), NOEC (No Effect Concentration) and LOEC (Lowest Effect 

Concentration) values. The lowest LC50, EC50, NOEC and LOEC for each species are presented 

below. Preferably, there are toxicological data on three taxonomic groups (i.e. algae, fish and 

crustacean), with endpoints on reproduction or growth. Mortality data does not give any good 

estimation for persistence or bioaccumulation, but is anyhow presented together with short- and 

long-term effect data, which together comprehends a fuller picture on the kinetics of the 

substance. 

The ecotoxicological data presented below is not to be considered as complete and only 

substances where relevant data has been available are presented. (IUPAC names derived from 

www.ebi.ac.uk/chebi/init.do and UN numbers derived from http://cameochemicals.noaa.gov/). 
MEPC 57/2/6 

ANNEX 

Page 34 

I:\MEPC\57\2-6.doc 

The toxicological data is derived from the following databases: 

http://cfpub.epa.gov/ecotox/advanced_query.htm, 

http://ecb.jrc.it/esis/, 

http://cameochemicals.noaa.gov/search?action=new&type=simple

http://www.ebi.ac.uk/chebi/init.do 

http://toxnet.nlm.nih.gov/

To further investigate the toxicity of the anolyte from the OS BWMS, an ecotoxicology search of 

the internal Active Substances and Relevant Chemicals has been performed. Ecotoxicological 

data has not been found for all substances, and not all data can be considered relevant for 

estimating the short- and long-term effects. N/a indicates that sufficient data has not been 

available. 

4.4.1 Hypochlorous acid 

4.4.1.1 Fish 

Effect Species End point Reference 

Acute aquatic 

toxicology 

Oncorhynchus 

kisutch, Coho salmon LC50: 32 μg/L/4 days Thatcher 1978 

Chronic 

aquatic 

toxicity 

Oncorhynchus 

gorbuscha, 

Pink salmon

NOEC: 42 μg/L/23 days, 

mortality Holland et al 1960 

4.4.1.2 Crustacean 

Effect Species End point Reference 

Acartia tonsa, Calanoid 

copepop

LC50: 403 μg/L/1 day Bradley et al 1997 Acute 

aquatic 

toxicology Americamysis bahia, 

Opossum shrimp

LC50: 143.6 μg/L/ 

7 days Fischer et al 1994 

Americamysis bahia, 

Opossum shrimp

NOEC: 47.8 μg/L/ 

7 days, reproduction Fischer et al 1994 

Americamysis bahia, 

Opossum shrimp

NOEC: 65.5 μg/L/ 

7 days, development Fischer et al 1994 

Chronic 

aquatic 

toxicity 

Americamysis bahia, 

Opossum shrimp

NOEC: 81.2 μg/L/ 

7 days, growth Fischer et al 1994 

4.4.1.3 Algae 

Effect Species End point Reference 

Chronic 

aquatic 

toxicity 

Porphyra yezoensis, Red 

algae

EC50: 1400 μg/L/ 

10 days, growth Maruyama et al 1988
MEPC 57/2/6 

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4.4.2 Hydrogen peroxide 

4.4.2.1 Fish 

Effect Species End point Reference 

Oncorhynchus mykiss, 

Rainbow trout

LC50: 10 000 μg/L/ 

4 days 

Office of Pesticide 

Programs, 2000 

Acute 

aquatic 

toxicology Lepomis macrochirus, 

Bluegill

LC50: 18 000 μg/L/ 

4 days 

Office of Pesticide 

Programs, 2000 

4.4.2.2 Crustacean 

Effect Species End point Reference 

Chronic 

aquatic 

toxicity 

Americamysis bahia,

Opossum shrimp

LC50: 47.8 μg/L/

7 days, reproduction Fischer et al 1994 

4.4.2.3 Algae

Effect Species End point Reference 

Acute aquatic 

toxicology 

Alexandrium 

tamarense, 

Dinoflagellate 

LC50: 10 000-50 000μg/L/0- 

3 days, reproductionGermination 

Ichikawa, S, 

Wakao, Y, 

Fukuyo, Y. 1993 

Chronic 

aquatic 

toxicity 

Porphyra 

yezoensis, Red 

algae 

LC50: 1400 μg/L/10 days, 

growth 

Maruyama, T 

et al 1988 

4.4.3 Ozone 

4.4.3.1 Fish 

Effect Species End point Reference 

Lepomis macrochirus, Bluegill LC50: 60μg/L/24hr Paller & 

Heidinger 1979 

Morone saxatilis, Striped bass LC50: 150μg/L/6hr Hall et al 1981 

Pimephales promelas, Fathead 

minnow LC50: 100μg/L/0.03hr Asbury & Coler 

1980 

Salmo gairdneri, Rainbow 

trout LC50: 9.3 μg/L/96 hr Wedemaier et al

1979 

Perca flavescens, Yellow 

perch

LC50: 

210μg/L/24hr/embryo Coler & Asbury 

1980 

Acute 

aquatic 

toxicology 

Salmo gairdneri, Rainbow 

trout

LC50: 190-310μg/L/ 

embryo 
MEPC 57/2/6 

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4.4.3.2 Crustacean 

No sufficient data available. 

4.4.3.3 Algae 

No sufficient data available. 

4.4.4 Chlorine dioxide 

4.4.4.1 Fish 

Effect Species End point Reference 

Salmo trutta, Brown 

trout 

LC50: 10 000 

000μg/L/48hrs 

Woodiwiss, FS, 

Fretwell, G. 1974 

Acute aquatic 

toxicology 

Rasbora heteromorpha, 

Harlequinfish, red 

rasbora 

LC50: 7 000 

000μg/L/24hrs 

Tooby, TE, Hursey, 

PA, Alabaster, JS. 1975 

4.4.4.2 Crustacean 

Effect Species End point Reference 

Carcinus maenas, Green / 

European shore crab 

LC50: 500 

000μg/L/48hrs 

Portmann, JE, 

Wilson, KW, 1971 

Acute aquatic 

toxicology 

Crangon crangon, Common 

shrimp 

LC50: 500 

000μg/L/48hrs 

Portmann, JE, 

Wilson, KW, 1971 

4.4.4.3 Algae 

Effect Species End point Reference 

Acute aquatic 

toxicology 

Macrocystis pyrifera, 

Giant kelp 

LC50: 

2500μg/L/48hrs 

Hose, JE, Fiore Di, D, Parker, 

HS, Sciarrotta, T. 1989 

4.4.5 Bromoform 

4.4.5.1 Fish 

Effect Species End point Reference 

Cyprinodon variegates, 

Sheapshead minnow 

NOEC: 2900μg/L/ 4 

days 

Heitmuller PT. 

et al 1981 

Cyprinodon variegates,

Sheapshead minnow 

LC50: 18000μg/L/96hrs 

Lepomis macrochirus, 

 Bluegill 

LC50: 29000μg/L/96hrs Boccafusco 

et al. 1981 

Acute 

aquatic 

toxicology 

Oryzias latipes, Japanese 

killifish/Medaka 

LC50: 40400μg/L/48hrs MITI 1992 

Chronic 

aquatic 

toxicity 

Cyprinodon variegatus, 

Sheepshead minnow 

LC50: 

>4800<8500μg/L/> 

28 days, Mortality, 

Maximum acceptable 

Toxicant Concentration 

Ward, GS. 

Parrish, PR, 

Rigby, RA, 1981 
MEPC 57/2/6 

ANNEX 

Page 37 

I:\MEPC\57\2-6.doc 

4.4.5.2 Crustacean 

Effect Species End point Reference 

Penaeus aztecus, 

Brown shrimp 

LC50: 20 000 μg/L/4 days Gibson, CI. 

et al 1981 

Acute aquatic 

toxicology 

Daphnia magna, 

Water flea

LC50: 46 000μg/L/48hrs LeBlanc 1980 

Daphnia magna,

Water flea 

EC50: 5400 μg/L/15days, 

reproduction 

Canton, JH. 

et al 1983 

Chronic 

aquatic 

toxicity Penaeus aztecus,

Brown shrimp 

LC50: 30-290μg/L 1-28days, 

accumulation, general 

Gibson, CI. 

et al 1981 

4.4.5.3 Algae 

Effect Species End point Reference 

Selenastrum 

capricornutum, 

Green algae

LC50: 18,7μg/L/24hrs 

Chlorophyll 

US EPA 1978 

 

Acute aquatic 

toxicology 

Selenastrum 

capricornutum, 

Green algae 

LC50: 28,1μg/L/96hrs 

Population changes, general 

US EPA 1978 

 

4.4.6 Dibromochloromethane 

4.4.6.1 Fish 

Effect Species End point Reference 

Acute aquatic 

toxicology 

Cyprinus carpio, 

Common camp 

LC50: 52 000 μg/L/ 45 min Mattie, JS. 

et al 1981 

4.4.6.2 Crustacean 

No sufficient data available. 

4.4.6.3 Algae 

No sufficient data available. 

4.4.7 Dichlorobromomethane 

4.4.7.1 Fish 

No sufficient data available. 

4.4.7.2 Crustacean 

No sufficient data available. 
MEPC 57/2/6 

ANNEX 

Page 38 

I:\MEPC\57\2-6.doc 

4.4.7.3 Algae 

No sufficient data available. 

4.4.8 2,4,6-Tribromophenol 

4.4.8.1 Fish 

Effect Species End point Reference 

Pimephales promelas, 

Feathered minnow 

LC50: 

6250μg/L/96hrs, 

Broderius, SJ, 

Kahl, MD, 

Hoglund, MD, 1995 

Pimephales promelas, 

Feathered minnow 

LC50: 6540μg/L/96hrs Geiger, DL, 

Northcott, CE, Call, 

DJ, Brooke, LT. 1985 

Acute aquatic 

toxicology 

Pimephales promelas, 

Feathered minnow 

LC50: 4500μg/L/ 

8 days 

Phipps, GL. et al 1981

4.4.8.2 Crustacean 

Effect Species End point Reference 

Acute aquatic 

toxicology 

Daphnia magna 

Water flea 

LC50: 1290 μg/L / 

2 days, 

Carlson, R. M, 

Caple, R. 1977 

4.4.8.3 Algae 

Effect Species End point Reference 

Acute aquatic 

toxicology 

Bacillariophyceae, 

Diatom 

LC50: 

500μg/L/48hrs, 

Physiology 

Erickson, SJ, 

Hawkins, CE, 1980 

Chronic aquatic 

toxicity 

Thalassiosira 

pseudonana, 

Diatom 

LC50: 

16 000μg/L/7days, 

population changes, 

general 

Erickson, SJ, 

Freeman, AE, 1978 

4.4.9 Dibromoacetonitrile 

4.4.9.1 Fish 

Effect Species End point Reference 

Acute aquatic 

toxicology 

Pimephales promelas, 

Feathered minnow 

LC50: 710μg/L/24hrs 

550μg/L/96hrs 

Mayes, MA, 

Blanchard FA, 

Hopkins, DL, 

Takahashi, IT, 1985 

4.4.9.2 Crustacean 

Insufficient data available. 
MEPC 57/2/6 

ANNEX 

Page 39 

I:\MEPC\57\2-6.doc 

4.4.9.3 Algae 

Effect Species End point Reference 

Glenodinium halli,

Dinoflagellate 

LC50: 16 000μg/L/7days, 

Population changes, 

general 

Erickson, SJ, 

Freeman, AE, 1978 

Chronic aquatic 

toxicity 

Scenedesmus 

subspicatus, 

Green algae 

EC50: 1400μg/L/72hrs, 

(Population changes, 

general) 

Kuhn, R, 

Pattard, M, 1990 

4.4.10 Monobromoacetic acid 

4.4.10.1 Fish 

Effect Species End point Reference 

Cyprinus carpio, 

Common carp 

LC50: 326mg/kg (100% 

mortality after 1.5hrs, 

force-fed), 222mg/kg 

LT100 (100% mortality 

after 5hrs, force-fed) 

Loeb, HA, 

Kelly, WH, 1963 

Acute aquatic 

toxicology 

Lepomis macrochirus, 

Bluegill 

LC50: 5ppm/24hrs 

(Solvents: Ethanol, 2-

Propanone, Multiple 

effects reported as one 

result) 

Applegate, VC, 

Howell, JH, 

Hall Jr. AE, 

Smith, MA, 1957 

4.4.10.2 Crustacean

Effect Species End point Reference 

Acute aquatic 

toxicology 

Daphnia magna, 

Water flea

EC50: 65 000μg/L/24hrs, 

behavior- equilibrium, 

intoxication-immobile) 

Kuhn, R. 1988, 

Kuhn, R. Pattard, 

M, Pernak K-D, 

Winter, A, 1989 

Chronic aquatic 

toxicity 

Daphnia magna, 

Water flea 

NOEC: 1600 μg/L/21 days, 

Reproduction Kuhn, R. et al 1989 

4.4.10.3 Algae 

Effect Species End point Reference 

Chronic aquatic 

toxicity 

Monoraphidium 

griffithii, 

Green algae 

EC50: 60μg/L/4 days, 

growth 

Eloranta, V 1982 
MEPC 57/2/6 

ANNEX 

Page 40 

I:\MEPC\57\2-6.doc 

4.5 Data on mammalian toxicity 

4.5.1 Hypochlorous acid 

4.5.1.1 Effects on skin and eye 

Exp. route Species Method Results Reference 

Skin Rabbit OECD 404 2% slight 

20% severe 

Sodium hypochlorite, 

IUCLID 2000; GESAMPBWWG 3/9 (MEPC 56/2/2) 

Eye Rabbit n/a 5.25% irritant 

0.5% slight 

irritant 

0.05% NOEC 

Sodium hypochlorite, 

IUCLID 2000; GESAMPBWWG 3/9 (MEPC 56/2/2) 

4.5.1.2 Corrosion/irritation 

Exp route Exp 

duration

Exp dose Species NOAEL Reference

Oral 90 days 200 mg/L in 

drinking 

water Sodium 

hypochlorite 

Mouse 50mg/L 

(10-12 

mg/kg/day) 

MEPC 56/2, 

paragraph 2.3.3.1 

(Daniel et al 1991) 

4.5.1.3 Sensitization data 

Exp route Species Method Results Reference 

Skin Guinea pig n/a 2.8% NOEC Sodium hypochlorite, IUCLID 

2000; GESAMP-BWWG 3/9 

(MEPC 56/2/2) 

4.5.1.4 Developmental and reproductive toxicity

Exp route Exp duration Exp dose Species NOAEL Reference

Oral 7 generations 100 mg sodium 

hypochlorite/L 

Rats 100 mg/L GESAMP -

BWWG 

4.5.1.5 Carcinogenicity 

Effect Species Method Results Reference 

Carcinogenicity Not 

carcinogetic 

GESAMP0-BWWG 

MEPC 56/2, paragraph 2.3.7.1 

Mutagenicity Not 

mutagenic 

GESAMP- BWWG 

MEPC 56/2, paragraph 2.3.7.1 
MEPC 57/2/6 

ANNEX 

Page 41 

I:\MEPC\57\2-6.doc 

4.5.2 Hydrogen peroxide 

Source: EU-risk assessment report ñ Hydrogen Peroxide. 

4.5.2.1 Effects on skin and eye 

Exp route Species Method Results Reference 

Skin Rat Whole body, 4 hours LC50: 2000 mg/m3 Kondrashov 

1977 

Eye Mouse Aerosols (70% H2O2) 

19000-9400 mg/m3

, 

30 min 

Gross opacies, 

microscopic eye 

lesions 

Punte et al 1953 

Inhalation Mouse Aerosols (70% H2O2), 5 

min -2 hrs, exp at 12000-

13000 mg/m3

50% lethality after 

10-15 min 

Punte et al 1953 

4.5.2.2 Corrosion/irritation 

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NOAEL NOE

L

Reference

Inhalation28 days 0-33 

mg/

m3

Rat 6 hrs 

daily for 

5 days 

per week 

Respiratory 

tract irritation, 

necrosis and 

inflammation of 

nasal cavity 

epithelium 

2.9 

mg/m3

14.6 

mg/

m3

CEFIC 

Peroxygen 

Sector 

Group 2002

Oral 12 weeks 0-

506 

mg/k

g 

bw/d 

Rat Stomach 

tube 

6 days 

per week 

Decreased bw 

gain, 

erythrocyte 

count, 

hemoglobin 

conc. Gastric 

mucosal 

erosions, 

eschars and 

round cell 

infiltration 

 56.2 

mg 

/kg 

bw/d 

Ito et 

al 1976 

Oral 0-90 

days 

0-

3000 

ppm 

Mouse Drinking 

water 

Decreased bw 

gain, reduced 

blood total 

protein, reduced 

food and water 

consumption, 

duodenal 

mucosal 

hyperplasia 

100 

ppm 

300 

ppm 

FMC 1997 
MEPC 57/2/6 

ANNEX 

Page 42 

I:\MEPC\57\2-6.doc 

4.5.2.3 Sensitization 

Exp route Species Method Results Reference 

Skin Human Vapour, 5 min-4 hr 

exposure 

NOAEL: 10 mg/m3, Effect 

conc/dose: 20 mg/m3

Kondrashov 

1977 

Inhalation Human Face mask (nose 

inhalation) 

NOAEL: 5 mg/m3, Effect 

conc/dose: 10 mg/m3

Kondrashov 

1977 

4.5.2.4 Developmental and reproductive toxicity 

Exp route Exp duration Species Method Results Reference

Oral 90 days Mouse Drinking 

water 

No 

effects 

FMC 1997 

4.5.2.5 Carcinogenicity 

Species Method Results Reference 

Mouse Drinking water Increased incidence of erosions 

and ulcer in the glandular 

stomach and duodenal 

hyperplasia 

Ito 

et al 1981a, 

Ito 

et al 1982b 

Hamster Painting of left buccal 

pouch twice weekly with 

DMBA* and H2O2

Development of carcinomas, 

hyperkeratosis and hyperplasia 

Weitzman 

et al 1986 

Mouse Dermal, treatment on 

dorsal skin with DMB*A 

and H2O2 and/or acetone 

twice weekly 

H2O2 functioned as an extremely 

weak tumor promoter 

KleinSzanto and 

Slaga 1982 

*9,10-dimethyl-1,2-bentzanthracene 
MEPC 57/2/6 

ANNEX 

Page 43 

I:\MEPC\57\2-6.doc 

4.5.2.6 Mutagenicity/genotoxicity 

Species Strain Measured 

endpoint 

Test 

conditions 

Results 

without 

activation 

Results 

with 

activation 

Reference 

Escherichia 

coli 

WP2 (uvrA) Ames test H2O2, 1.0-

3333.3μg/pla

te 

- - SRI 

International 

1980 

Salmonella 

typhimurium 

TA1535/pS 

K1002 

DNA damage 

and repair 

H2O2, 

45μg/ml 

+ NT Nakamura 

et al 1987 

African green 

monkey 

Kidney 

cells (CV-1) 

Mammalian 

cell-line 

mutation ñ 

(supF locus of 

the pZ189 

plasmid 

mutations) 

H2O2, 0.5-

10mM 

+ NT Moraes 

et al 1990 

Chineese 

hamster 

V79-379A 

cells 

DNA damage 

and repairñ

DNA single 

and doublestrand breaks 

H2O2, 10-

1000 μM 

+ NT Prise 

et al 1989 

4.5.3 Ozone 

4.5.3.1 Corrosion/Irritation 

Exp route Species Method Results Reference 

Oral Human Inhalation 

0.021-0.124 ppm/29 min 

Decremented FVC, 

FEV1, PEFR 

Spektor et al 1988 

Oral Human Inhalation 

0.08ppm/6.6hrs 

Decremented FVC, 

FEV1Increased SRaw 

McDonnell 

et al 1991 

4.5.3.2 Repeated-dose toxicity 

Exp duration Exp 

dose

Species Results Reference

8 hrs/day day 6-9, 9-12 

and 6-15 of gestation 

1.97 

ppm 

Rat Increased resorption rate Kavlock et al 1979 

day 17-20 of gestation 1.0 or 

1.5 

ppm 

Rat Offspring with retarded of 

reflex development and 

slowing in open field 

behaviour 

Kavlock et al 1980 
MEPC 57/2/6 

ANNEX 

Page 44 

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4.5.3.3 Developmental and reproductive toxicity 

Exp 

duration

Exp dose Species Method Results Reference

Day 17-20 of 

gestation 

2 and 2.9 

mg/m3

Rat 

(offspring) 

Maternal 

exposure 

Retarded reflex 

development, slowing 

open field behaviour 

Kavlock 

et al 1980 

7hrs/day, 5 

days/week 

0.4 mg/m3 Mouse (fetus) Maternal 

exposure 

Blepharophimosis and 

jaw anomalies 

Veninga 

1967 

6 hrs 2 mg/m3 Rat 

(pregnant/ 

lactating) 

 Enhanced sensitivity 

to o3 pulmonary 

inflammation 

Gunnison 

et al 1992 

4.5.3.4 Carcinogenicity 

Ozone is not considered as carcinogenic (The American Conference of Governmental Industrial 

Hygienists (ACGIH)). 

4.5.4 Chlorine dioxide 

Very limited data available, probably due to the fact that chlorine dioxide is readily decomposed 

to chlorine and oxygen in the environment. 

4.5.4.1 Acute toxicity 

Species Exp route Type Value Reference 

Rat Oral LD50 292 mg/kg bw Finnish Chemicals Oy ƒets‰ 

Rat Inhalation LCLo 500 ppm Finnish Chemicals Oy ƒets‰ 

4.5.4.2 Skin and eye irritation 

Organ Species Remark Reference 

Skin Human May irritate skin very slightly Finnish Chemicals Oy ƒets‰ 

Eye Human Vapours may irritate eyes Finnish Chemicals Oy ƒets‰ 

4.5.4.3 Carcinogenicity 

Chlorine dioxide is not classified carcinogenic (Finnish Chemicals Oy ƒets‰). 

4.5.5 Bromoform 

4.5.5.1 Acute toxicity

Exp route Value Species Reference/comments 

Oral LD50 (mg/L) 707-1550 Rats & Mice EHC 216, 2000; 

GESAMP-BWWG 

Inhalation LC50

(mg/L/4h) 

7000μ/L Dogs Death after 1h 

GESAMP- BWWG 
MEPC 57/2/6 

ANNEX 

Page 45 

I:\MEPC\57\2-6.doc 

4.5.5.2 Repeated dose toxicity 

Exp route Exp 

duration

Exp dose Species NOAEL Reference

Oral 13 weeks 25mg/kg/day (rat), 

100mg/kg/day 

(mice) 

Rats and 

Mice 

25mg/kg/day 

(rat), 

100mg/kg/day 

(mice) 

EHC 216 (2000) 

4.5.5.3 Corrosion/Irritation

Exp route Species Method Results Reference 

Skin Human Not specified Irritant MSDS, 

GESAMP-BWWG 

Eye Human Not specified Irritant MSDS, 

GESAMP-BWWG 

Inhalation LC50

(mg/L/4h) 

Human 0.03-1.2 μg/L Irritant MSDS, 

GESAMP- BWWG 

4.5.5.4 Developmental and reproductive toxicity 

Exp route Exp 

duration

Exp 

dose

Species Results Reference

Oral At days 6-15 

of gestation 

50, 100 

and 200 

mg/kg/ 

day 

Rats Evidence of foetotoxic 

response. 

No foetal 

malformations 

observed 

EHC 216 (2000) 

Oral 105 days Rats 

(male 

and 

female 

pairs) 

No detectable effect on 

fertility, litters/pair, 

live pups/litter, 

proportion of pups born 

alive, sex or body 

weights 

EHC 216 (2000) 

4.5.5.5 Carcinogenicity 

Effect Species Method Results Reference 

Carcinogenicity Rats 5 days exposure/week 

for 2 years 

No evidence 

observed 

NTP, 1989a 

Mutagenicity Bacteria 

Not 

identified 

(Ames test) In vivo Mutagenic 

inconclusive 

Reprotoxicity Rats 5 days exposure/week 

for 2 years 

No evidence 

observed 

NTP, 1989a 

4.5.6 Dibromochloromethane 

Trihalomethanes in drinking water: WHO/SDE/WSH/05.08/64. 
MEPC 57/2/6 

ANNEX 

Page 46 

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4.5.6.1 Acute toxicity 

Exp route Value Species Reference 

800 Mouse MEPC 56/2, paragraph 2.3.1.2; 

GESAMP- BWWG 

Oral LD50 (mg/L) 

1186/848 

(male/female) 

Rat Chu et al. 1980 

4.5.6.2 Repeated dose toxicity 

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NOAEL Reference

Oral 90 days 0-200 

mg/kg/

d 

Rat Solved 

in corn 

oil, 

gavage 

Decrease in body 

weight at 200 

mg/kg/d, elevated 

alanine 

aminotransferase, 

centrilobular 

hepatic necrosis, 

kidney proximals 

tubule cell 

degeneration 

50 

mg/kg/d 

MEPC 56/2, 

para. 2.3.1.2 ; 

GESAMP ñ 

BWWG ; 

Daniel 

et al 1990 

Oral 90 days 0-250 

mg/kg 

bw/day 

Rat Solved 

in corn 

oil, 

gavage 

Depressed body 

weight, increased 

hepatic 

vacuolation, 

kidney and liver 

toxicity 

30 

mg/kg 

bw 

NTP 1985 

Oral 90 days 0-250 

mg/kg 

bw/day 

Mouse Solved 

in corn 

oil, 

gavage 

Kidney and liver 

toxicity 

125 

mg/kg 

bw 

NTP 1985 
MEPC 57/2/6 

ANNEX 

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4.5.6.3 Developmental and reproductive toxicity

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NOAEL NO

EL

Reference

Oral 2 

generati

ons 

0.4 

mg/L 

Mice At 4 mg/L 

decreased 

fertility. No 

dominant lethal 

or teratogenic 

effects observed. 

n/a n/a MEPC 

56/2 para. 

2.3.5.2 

GESAMPBWWG 

Oral 35 days 

/generati

on 

0-685 

mg/kg 

bw (0-

4000 

mg/L) 

Mice Ad 

libitum,

multige

neratio

nal 

Decreased body 

weight, enlarged 

livers with gross 

morphological 

changes, 

decreased litter 

size, decreased 

pup viability, 

reduced fertility 

and reduced F1

generation 

survival 

17 

mg/kg 

bw/day 

n/a Borzelleca 

& 

Carchman 

1982 

4.5.6.4 Carcinogenicity 

Effect Species Method Results Reference 

Carcinogenicity Human Probable 

human 

carcinogen 

US EPA (Iris) 

MEPC 56/2, 

para 2.3.6.2; 

GESAMP- BWWG; 

Mutagenicity Salmonella 

typhimurium 

Ames Positive and 

negative 

results 

MEPC 56/2, 

para. 2.3.7.2; 

GESAMP- BWWG 

Genotoxicity Chinese hamster 

ovary cells 

Human lyphocytes 

Chromosoma

l aberration 

test 

SCE-test 

Positive 

Positive 

Ishidate et al 1982 

Morimoto & 

Koizumi 1983 

4.5.7 Dichlorobromomethane 

Trihalomethanes in drinking water: WHO/SDE/WSH/05.08/64. 

4.5.7.1 Acute toxicity 

Exposure route Value Species Reference 

Oral LD50 (mg/L) 916/969 (male/female) Rat Chu et al. 1980 
MEPC 57/2/6 

ANNEX 

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4.5.7.2 Repeated dose toxicity 

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NOAEL Reference

Oral 90 days 0-300 

mg/kg 

bw/ 

day 

Rat Gavage Decreased 

body weight, 

centrilobular 

degeneration 

of liver, 

degeneration 

and necrosis 

of kidney 

75 and 150 

mg/kg 

bw/day (bw 

reduction 

and 

hepatic/rena

l lesions 

respectively) 

NTP 1987 

Oral 90 days 0-100 

(m) 

/0-

400 

(f) 

Mouse 

(m/f) 

Gavage Centrilobular 

degeneration 

of liver (f), 

degeneration 

and necrosis 

of kidney (m) 

50 mg/kg 

bw/day 

NTP 1987 

4.5.7.3 Developmental and reproductive toxicity 

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NOAEL Reference

Oral 15 days 

(d6-21 of 

gestation) 

0-82 

mg/kg 

bw/day 

Rat Ad 

libitum

Water 

comsumption, 

body weight 

gain and feed 

consumption 

reduced 

18.4 mg/kg 

bw/day 

(maternal) 

45 mg/kg 

bw/day 

(developmental) 

Christian 

et al. 

2001 

Oral 23 days 

(d6-29 of 

gestation) 

0-55.3 

mg/kg 

bw/day 

Rabbit Ad 

libitum

Body weight 

gain and feed 

consumption 

reduced 

13.4 mg/kg 

bw/day 

(maternal) 

55.3 mg/kg 

bw/day 

(developmental) 

Christian 

et al. 

2001 

Oral 52 weeks 22 and 

39 

mg/kg 

bw/day 

Rats Ad 

libitum

Decreased 

mean straight 

line average 

path and 

curvilinear 

velocities of 

sperm 

 IPCS 

2000 
MEPC 57/2/6 

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4.5.8 2,4,6-Tribromophenol 

4.5.8.1 Effects on skin and eye

Exp route Species Method Results Reference 

Skin (LD50) Rabbit 

Rabbit 

 >2000 mg/kg bw 

>8000 mg/kg bw 

IRDC 1973 

IRDC 1974a 

Inhalation LC50

(mg/L/4h) 

Rat 

Rat 

4h 

1h 

50 000 mg/m3

200 000 mg/m3

IRDC 1974a 

IRDC 1973 

4.5.8.2 Repeated dose toxicity 

Exp 

route

Exp 

duration

Exp 

Dose

Species Method Results NOAEL Reference

Oral 48 days 100-

1000 

mg/kg 

bw/ 

day 

Rat Gavage Salivation, suppressed bw 

gain, decreased food 

consumption, increased 

liver weight, increased 

kidney weight, increased 

total protein, decreased 

bilirubin and potassium in 

blood, decreased thymus 

weight, hepatocyte 

hypertrophy, decreased 

hepatic fatty change, 

renal papillary necrosis 

and dilatation of tubules, 

lymphycyte infiltration 

100 mg 

/kg bw

Tanaka 

et al 1999 

4.5.8.3 Corrosion/irritation 

Exp route Species Method Results Reference 

Skin Rabbit OECD TG 404 

One dosage (0.5g) 24h 

Not irritating DSBG/BCL 

(1985b) 

Eye Rabbit OECDTG 405 

One dosage (100mg) 

Moderately irritating DSBG/BCL 

(1997b) 
MEPC 57/2/6 

ANNEX 

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4.5.8.4 Developmental and reproductive toxicity 

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NO 

AEL

NOEL Reference

Oral Day 0 

and day 4 

100, 

300 

and 

1000 

mg/kg/

day 

Rat Repeated 

dose 

toxicity, 

reproduct

ion/devel

opment 

Reduced 

viability and 

body weight 

 1000 

mg/kg/day 

mother 

300 

mg/kg/day 

pups 

Tanaka 

et al 1999 

Oral 20 days 10-

3000 

mg/kg/

day 

Rat Decreased 

weight gain, 

increased post 

implantation 

loss, decreased 

fetus viability 

 1000 

mg/kg/day 

mother 

300 

mg/kg/day 

pups 

IRDC, 

1978b 

Inhala

tion

21 days 

of 

gestation 

0.03-

1.0 

mg/m3

Rat Whole 

body 

inhalation 

Pre and post 

implantation 

embryo losses, 

decreased fetal 

body weight 

<0.03

mg/m3

 Lyubimov 

et al 1998 

4.5.8.5 Carcinogenicity 

No long-term exposure or carcinogenicity studies on brominated phenols were identified. 

4.5.8.6 Genotoxicity

Effect Species Method Dose Results Reference 

Genotoxicity CHL/IU 

 cells 

Chromosoma

l aberration 

test (in vitro) 

1.6 mg/ml Positive Sasaki 

et al 1999 

Genotoxicity Mouse, 

 bone marrow 

Micronucleus 

test (in vivo) 

75-300 

mg/kg 

intraperiton

eally 

Negative DSBG 

/BCL (2002) 

4.5.9 Dibromoacetonitrile 

Halogenated Acetonitriles in Drinking-water: WHO/SDE/WSH/03.04/98. 
MEPC 57/2/6 

ANNEX 

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4.5.9.1 Repeated dose toxicity 

Exp 

route 

Exp 

duration

Exp 

dose

Species Method Results NOAEL Reference

Oral 13 weeks 0.9-

12.6 

mg/kg 

bw/da

y 

Rat Drinking 

water ad 

libitum

Decreased 

water 

consumption, 

decreased 

body weight 

11.3 

(females) 

and 12.6 

(males) 

mg/kg 

bw/day 

NTP, 

2001b and 

2002 a,b 

Oral 14 days 23-280 

mg/kg 

bw 

Rat Gavage Decreased 

body weight 

in males, 

increased 

liver weight 

in females 

23 mg/kg 

bw/day 

Hayes 

et al. 1986 

4.5.9.2 Developmental and reproductive toxicity 

Exp 

route 

Exp 

duration

Exp dose Species Method Results NOAEL Reference

Oral 14 days 2-18 

mg/kg 

bw/day 

Rat Drinking 

water, ad 

libitum

Decreased testes 

weight and 

testicular atrophy 

12 mg/kg 

bw/day 

NTP, 

2000c 

14 days 

(gestation 

day 7-

21) 

50mg/kg 

bw/day 

Rat Intubation Decreased 

maternal weight 

gain, decreased 

birth weight* 

50 mg/kg 

bw/day** 

Smith 

et al. 1987 

* Dibromoacetonitrile were solved in tricaprylin which is proven to be a development 

toxicant and hence possibility of potentiating developmental effects of trihaloacetonitriles 

and probably other haloacetonitriles. 

** only one dose administered. 

4.5.9.3 Genotoxicity 

Effect Species Method Results Reference| 

DNA 

damage 

Escherichia 

coli 

SOS 

chromotest 

Weakly positive 

(without metabolic 

activation) 

Le Curieux 

et al. 1995 

Sister 

chromatid 

exchange 

Chinese 

hamster ovary 

cells 

Exogenous 

metabolic 

activation 

Induction Bull et al. 1985 

 Human 

lymphoblastic 

cells 

 DNA strand breaks Daniel et al 1986 
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4.5.10 Monobromoacetic acid 

No data on mammalian toxicology for Monobromoacetic acid from the current databases is 

available. 

5 HANDLING AND USE OF THE OS BWMS

5.1 General 

A complete set of documentation describing the OS BWMS and particulars of the specific 

installation follows each delivery. A set of such is enclosed to this application describing the 

system as installed on board the M/V Hˆegh Trooper. The system documentation includes 

arrangement drawings, data and specification sheets, operational manuals and spare part references. 

With all standard components such as pumps, compressors, the nitrogen generator, etc., the 

suppliersí documentation is also enclosed. 

The operational manual provides information enabling proper use of the system and includes 

safety instructions and maintenance programme. Officers and crew members involved in ballast 

water operations and/or the maintenance of ballast water systems should be made familiar with 

all features of the OS BWMS and further should undergo training in the operation and 

maintenance of all such features. 

In the following, the main system components are described. In addition to the focused systems, 

there are some supporting systems and components such as filter, valves, pumps, etc. These are 

not described in detail here as they are of standard design and well known to both crew and 

officers. Their usage, maintenance requirements, etc., are, however, included in the OS BWMS 

documentation and training package. 

5.2 Circumferential cavitation ñ C3T 

The cavitation unit is a static and passive component integrated into the main ballast water pipe, 

as illustrated in Figure 5 below. The sub-unit cavitation devices and energy release zones are 

constructed from a homopolymer with approximately one-third of the tensile strength of steel. 

The material has a melting point at 175°C. However, all components made from this material are 

insulated and built-in into a pipe casing as a section of the standard piping in the engine room. 

Thus, in the case of an engine room fire, a potential melting of the components constructed from 

homopolymer will not affect the integrity of the ballast water system. 

The cavitation chamber may be periodically checked by installing hydrophones. OceanSaver has 

developed a control programme used for commissioning that will verify the cavitation 

characteristics of the system. 

Cavitation is usually associated with erosion, e.g. particularly problems in propulsion as well as 

in pump impellers. This is a phenomena arising as a consequence of the release of high pressure 

pulses as cavities (bubbles) generated are exposed to a higher internal fluid pressure and 

implodes. The C3T unit applies this released energy to the flow direction of the water using 

surfaces and geometry to initiate cavitation. This application avoids direct exposure to these 

surfaces. However, the components in the energy zone are considered as replacement parts with 

an expected life span of 3 years operation. The C3T delivery includes one set of replacement 

cassette (C3T sub-unit). Replacement should be made after 3 years or 2000 hrs operations. 
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The automation system will provide a reminder. Replacement is simple and can be undertaken by 

trained crew. 

Figure 5: C3T unit including 18 C3T sub-units. 

5.3 The C2E unit

The C2E unit is a self contained fully automatic pressurized close-circuit modular system. It has 

built in redundancy which allows periodic use of individual modules and the availability of 

spares if a system module fails. 

The C2E unit comprises four main components: 

- Control/ automation and monitoring including calibration; 

- Power supply/ converter; 

- Electrodialytic cell modules;and 

- Ventilation loop. 

These components are built into a singular cabinet that may be located independently from the 

actual location of the ballast water line and associated components. The cabinet configuration 

depends upon the planned location of the unit, e.g. for the installation in potential dangerous 

areas specific requirements will apply to the cabinet and all its connections. 

Features include a calibration loop which at set intervals is activated to calibrate operational 

characteristics appropriate for the water in which the vessel is operating in as well as automated 
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cleaning by reverse charge following ballasting operations. Options are in place allowing vessels 

periodically operating in fresh water to be fitted with the system. 

The actual cell modules are automatically cleaned by applying reverse charge. Apart from this 

cleaning process, there are no required maintenance requirements other than a system check 

co-ordinated with the vessels general maintenance programme/class procedures. 

The C2E unit is built in accordance with all relevant standards and regulations and its actual 

specific installation is subject to class approval. 

5.3.1 Training

Training in the safe operation and maintenance of the C2E equipment and its safe application 

on board the ship is provided upon commissioning to the ship's officers and crew. New crew 

members should be trained promptly. Training must include the following: 

.1 safe operation of the C2E uni; and 

.2 awareness of system performance during operation. 

There are no handling or storage issues involved in the operation of this system. Hazards awareness 

associated with potential fume build up is especially important for all the officers. 

5.3.2 Fire-fighting measures

There are neither special fire-fighting requirements for the solutions produced by the C2E unit 

nor for the processes applied for their production. The C2E disinfectant is regarded as not 

flammable. 

5.3.3 Safety issues ñ Precautions

All components used in the C2E system are approved for shipboard use. Electrical components, 

pressure components and other system components are fully compliant with all relevant class 

requirements. 

Installation precaution: 

- Ensure that the chosen location for the system is qualified with respect to 

operational conditions (temperature/ humidity/ ventilation). 

- The unit may be affected by strong magnetic fields. To ensure durability, 

installation on vibration dampening is advised. 

Ventilation

The C2E cabinet is equipped with internal ventilation to ensure proper cooling and efficient 

evacuation of any gas that may be generated during operations. As the system is pressurized and 

close-circuited, any gas produced is rapidly compressed and partly re-dissolved. There are no 

releases of any gas, fumes or vapor to the immediate vicinity unless a malfunction occurs. When 

the C2E disinfectant re-enters the main ballast water line, any remaining gas is further diluted 

and re-dissolved in the water. Safety is further enhanced by gas monitoring sensors on the 
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exhaust side of the internal ventilation system monitoring potential accumulated chlorous gases 

and hydrogen. This is incorporated in the automation system. Elevated levels will initiate the 

auto-stop function of the unit. It should be noted that the systems close circuit design prevent any 

direct exposure of the electrodialytic process to atmosphere; further, that no residuals are 

produced avoiding potential vapor-off. This reduces the potential formation of gas in the cell 

cabinet considerably. The powering of the unit compared to the flow over the cell is a further 

safety feature limiting any production of hydrogen to less than those creating explosive 

atmospheres with a safety margin of 4. 

 

Electrical connections 

All electrical components and connections included in the C2E unit are built according to 

regulations for shipboard use. Connections from the ships supply to the C2E unit must be 

according to current electrical requirements and carried out by qualified licensed personnel. 

Ensure that the electrical supply is compliant with the requirements of the unit. (380 Volts, each 

phase 16A). The unit must be earthed. 

Maintenance 

The C2E unit must not be opened by unauthorized personnel. All servicing should be referred to 

trained and qualified service personnel. 

5.4 Handling and use of the Nitrogen Supersaturation Unit 

5.4.1 General

The Nitrogen supersaturation unit compresses air which is fed through a membrane-based 

nitrogen generator to produce nitrogen. The nitrogen is then injected into a portion of the ballast 

water taken off the main line and mixed over a static mixer. This flow is then re-injected into the 

main pipe and mixed again resulting in supersaturation. As a consequence of this, oxygen 

dissolved in the ballast water is released. 

Both the compressor as well as the membrane based nitrogen generator are standard components 

supplied for shipboard use. The injection components are passive units with the exception of a 

pump, again a standard unit designed, built and certified for shipboard use. 

On-board produced nitrogen has an oxygen content of approximately 0.5% by volume. 

This makes the inert nitrogen gas a non-toxic but asphyxiating gas which must not be inhaled. 

The nitrogen producing components may be installed independently of the ballast water pipe. 

However, whatever location is chosen requires to have appropriate ventilation. 

The nitrogen system is a pressurized system operating at 4 to 6 bar. Working pressure is set for 

the individual installation. Any pressure loss in the system will initiate an alarm and system 

auto-stop. 
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5.4.2 Precautions to be observed at all times

.1 At no time shall any person enter any space under Nitrogen gas treatment or any 

space with potential Nitrogen gas migration and an Oxygen deficient atmosphere 

without breathing equipment or before it is thoroughly ventilated and checked. 

.2 All access to spaces under Nitrogen gas or areas under potential Nitrogen gas 

migration are locked, secured and clearly marked with ìDangerousî warning signs 

made up in English and all applicable languages are to be exhibited at all 

manholes. 

.3 Ballast tank manholes under Nitrogen gas treatment must never be opened and 

entered without the correct procedures being carried out. 

.4 In an Emergency situation, the valve for the Nitrogen gas system is locked with a 

padlock. The key for the valve will be held by the following crew: Master, Chief 

Engineer, Chief Officer, Second Engineer. 

5.4.3 Training

Training in the safe operation and maintenance of N2 equipment and its safe application aboard 

ship is to be given to the shipís officers and crew. New crew members should be trained 

promptly. Training must include the following: 

.1 recognition of posted danger placards; and 

.2 awareness of the properties of Nitrogen. 

Nitrogen hazard awareness is especially important for all the officers. 

5.4.4 Handling and Storage 

Safety equipment must be available when dealing with Nitrogen gas. The minimum complement 

of safety equipment should include: 

 .1 Portable oxygen monitor ñ A Nitrogen filled space is dangerous because of the 

low oxygen content of the atmosphere. A Nitrogen filled compartment (ballast 

tank) typically contains less than 5% oxygen. It is therefore essential to have the 

correct instrumentation, this being, a portable oxygen monitor to assess the level 

of oxygen within the space before entering. It is also essential that this instrument 

is properly calibrated. Fresh air with a standard oxygen concentration of 21% is 

used in calibration. 

 .2 Warning signs in applicable languages ñ A Nitrogen-filled space should be 

clearly labelled with caution and danger signs. Manholes must be bolted prior to 

the Nitrogen treatment being started and kept closed until the Nitrogen supply has 

been turned off, the space gas freed, and declared safe to enter. 

Storage: The nitrogen consumption is supplied on demand and thus, there are no storage 

requirements. However, for certain applications, Nitrogen may be supplied produced for storage 

or delivered from existing on-board Nitrogen facilities. In any such case, all systems will be 
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designed and built according to relevant requirements. Any such systems will be subject to class 

approval. 

It is important that the ships crews are familiar with the symptoms of asphyxiation whilst 

working with Nitrogen and the concentrations at which this can occur. The following table 

provides a guideline to these symptoms: 

Table 5: Symptoms of asphyxiation 

Oxygen % Symptom 

21% Breathing, all functions normal. 

19-19.5% Oxygen monitor alarm level. 

17% Candle is extinguished. 

12-16% Breathing rate is increased and pulse rate accelerated. Ability to 

maintain attention and to think clearly is diminished, but can be 

restored with effort. Muscular coordination for finer skilled 

movement is disturbed. 

10-14% Consciousness continues but judgement becomes faulty. Severe 

injuries, burns, bruises etc., may cause no pain. Muscular effort 

leads to rapid fatigue, may permanently damage the heart and cause 

fainting. 

6-10% Nausea and vomiting may appear. Legs give way; person cannot 

walk, stand or crawl. This is often the first and only warning and it 

comes too late. The person may realize he is dying but does not 

care. No pain is felt. 

Less than 6% Loss of consciousness in 30-45 seconds if resting, sooner if active. 

Breathing in gasps followed by convulsive movements, then 

breathing stops. The heart may continue beating for a few minutes 

then it stops. 

When an individual is exposed to a low oxygen concentration, asphyxiation will occur quickly 

and without any warning sign. To an observer, the symptoms of oxygen deprivation are 

increased pulse and breathing rate. To the exposed individual, the symptoms are fatigue, 

abnormal perceptions or responses, dry throat, headache and sickness. 

Exposure to an atmosphere with a low concentration of Oxygen does not necessarily produce 

recognizable symptoms before unconsciousness occurs. The onset of brain damage and the risk 

of death can follow within a few minutes. If the oxygen deficiency is not sufficient to cause 

unconsciousness, the mind is liable to become apathetic and complacent, and even if these 

symptoms are noticed and escape is attempted, physical exertion will aggravate the weakness of 

both the mind and the body. 

Persons showing signs of oxygen deprivation should be moved immediately to a normal 

atmosphere. If the person is unconscious, check for pulse and breathing. Continue to monitor 

vital life signs. If the pulse or breathing has stopped, cardiopulmonary resuscitation (CPR) must 

be carried out. If both pulse and breathing are present, the person should recover without 

assistance. 

There is a danger to shipsí crew and shore personnel of Nitrogen gas escaping or migrating into 

spaces adjacent to a Nitrogen-filled space. It is important to recognize that a hazard may exist 
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and that sufficient ventilation precautions are observed prior to entering or approaching areas 

where Nitrogen gas may exist. Some of these spaces may be as follows: 

.1 Expected Spaces ñ Ballast tanks, air ventilation pipes from tanks; 

.2 Unexpected Confined Spaces ñ Cable trunks, nitrogen generating area; and 

.3 Known Nitrogen Migration Paths ñ Piping and electrical cable penetrations. 

After a space is ventilated thoroughly, it is necessary to check the atmosphere at different heights 

and locations to ensure that no pockets of oxygen-deficient atmosphere remain. It must be 

remembered that inert gas/Nitrogen is slightly lighter than air in general. 

5.4.5 Emergency measures 

Measures should be integrated in the vessels general safety plan. 

Emergency first aid 

In the event that a rescue needs to be carried out from an area under Nitrogen gas treatment the 

following procedure will be adopted: 

.1 raise the alarm by informing the bridge or duty deck officer; 

.2 close all CA control valves to the appropriate CA zones; 

.3 open all inlet and outlet vents on the fresh air system to the appropriate zones; 

.4 commence maximum fresh air ventilation; 

.5 assemble emergency/recovery team and equipment; 

.6 when normal atmosphere has been achieved rescue becomes possible; and 

.7 when rescue is made, continue to monitor vital life signs and carry out appropriate 

first aid and recovery procedures. 

Fire-fighting measures 

Nitrogen is a true inert gas and is non-explosive. It does not represent a fire hazard. 

Accidental release 

In the event of Accidental release, the following procedure will be adopted: 

.1 maximum fresh air ventilation must be carried out to make that zone and passages 

to the zone free from Nitrogen; 

.2 entry into confined spaces may only be carried out after completion of ìPre entry 

proceduresî by the Shipís Safety Officer; 

.3 after the Nitrogen generator has been shut down, the supply valves locked and the 

Nitrogen spaces ventilated, each of the adjacent spaces must be ventilated; and 

.4 when all ventilating has been accomplished for the entire ship, the N2 warning 

signs should be removed or covered. 
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6 RISK CHARACTERIZATION 

6.1 Screening for persistency, bioaccumulation and toxicity 

Criteria for evaluating the long-term persistence, bioaccumulation and toxicity, the so-called 

PBT criteria have been decided by several organisations and in several protocols and policies. 

The EU PBT criteria have decided the following criteria for persistence, bioaccumulation and 

toxicity (Table 6). 

Table 6: Criteria for identification of PBT substances 

Criterion PBT Criteria 

P Half-life > 60 d in marine water or > 40 d in freshwater or half-life 

> 180 d in marine sediment or > 120 d in freshwater sediment 

B BCF > 2,000 

T Chronic NOEC < 0.01 mg/L or CMR or endocrine disrupting 

effects 

6.1.1 The P criterion 

None of the Active Substances or the Relevant Chemicals has a half-life exceeding 60 days in 

marine water. Subsequently, there is no Active Substance or Relevant Chemical within the OS 

BWMS that fulfils the P criterion for being persistent. 

6.1.2 The B criterion 

The B criterion can be decided by calculating the BCF (bioconcentration factor, weight basis) for 

each substance. If BCF values are not at hand, as here is the case, the relation between BCF and 

the octanol/water partition coefficient can be described as: 

log BCF = 0.85 ⋅ logKow − 0.70 (Ref. TGD part II p. 126)

Therefore, a log Kow value has been calculated for each substance to give a corresponding BCF 

presented in Section 4. Nevertheless, most substances produced in the electrolysis of 

the OS BWMS are in ionic form, and ions are in general considered to accumulate 

to insignificant extents. The log Kow hereby presented, and the corresponding BCF values 

can confirm that observation. Octanol/Water partition coefficient, logP are derived from 

http://www.molinspiration.com/cgi-bin/properties. 

It can be concluded that none of the chosen Active Substances or Relevant Chemicals can be 

addressed as being bio accumulative. 

6.1.3 The T criterion 

To fit the T criterion the NOEC value of the substance shall be < 0.01 mg/L. According to the 

ECOTOX database search presented in Section 4, only chlorine fits that criterion with an LC50

for the Acartia tonsa of 5μg/L. 
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6.2 PEC ñ PNEC assessment 

6.2.1 PNEC estimation

If sufficient toxicity data is at hand, a PNEC (Predicted No Effect Concentration) value for an 

Active Substance or Relevant Chemical can be derived, by using the systematic approach 

described in the Technical Guidance Document on Risk Assessment by the European Chemicals 

Bureau, part II (TGD). The PNEC value is the best indicative for evaluating the toxic behaviour 

of the Active Substances and Relevant Chemicals. 

A PNEC value can be estimated by using the assessment factors proposed in the Technical 

Guidance Document on Risk Assessment by the European Chemicals Bureau, part II (TGD II). 

The notes (a), (b), (c) and (d) can be found on page 149 in the Technical Guidance Document on 

Risk Assessment by the European Chemicals Bureau, part II. 

There is no sufficient data available for estimating PNEC values for all above presented Active 

Substances and Relevant Chemicals. Derived PNEC values are given in Table 7. 
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Table 7: Estimated PNEC values for Active Substances and Relevant Chemicals 

Toxic substance Available data Assessment 

factor PNEC 

Hypochlorous acid 

Two long-term NOECs from freshwater 

or salt-water species representing two 

trophic levels 

500 0.096 μg/L 

Bromoacetic acid 

Two long-term NOECs from freshwater 

or salt water species representing two 

trophic levels 

500 0.12 μg/L 

Tribromomethane 

One short-term EC50 from each of three 

trophic levels of the base set (fish, 

Daphnia and algae), but where at least the 

acute toxicity for Daphnia is determined. 

10 000 0.29 μg/L 

2-Bromophenol One long-term NOEC from freshwater or 

salt water crustacean reproduction 1000 0.22 μg/L 

Chlorine dioxide 

LC50 values from two freshwater fish 

species, marine crustacean and marine 

algae 

10 000 0.25μg/L 

Ozone LC50 values from 6 freshwater fish 10 000 0.93ng/L 

Bromoform 

LC50 from two freshwater fish, one 

freshwater and one marine crustacean and 

one freshwater algae 

1000 0.29μg/L 

Dibromochlorome

thane LC50 from one fish species 10 000 5.2μg/L 

2,4,6 

Tribromophenol 

LC50 from one fish species (3 studies), 

one crustacean and one algae. Chronic 

effects from one algae 

1000 0.5μg/L 

Dibromoacetonitrile LC50 from one fish species, chronic 

effects from two algae 10 000 0.055μg/L 

Monobromoacetic 

acid 

LC50 from 2 fish species and one 

crustacean. Chronic effects on one 

crustacean and one algae 

1000 1.6μg/L 

The lowest PNEC value is derived for Ozone with a PNEC of 0.93 ng/L. However, Ozone has a 

half-life around 5.3 seconds in seawater and is produced in low concentrations of the C2E unit. 

Ozone is, therefore, not relevant in a PEC ñ PNEC assessment for ballast water discharged at 

least 24 hours after treatment. Taking into account the half-life and other data presented in 

section 4, the most Relevant Chemical compound seems to be hypochlorous acid, with a PNEC 

value of 0.096 μg/L. 

6.2.2 PEC values in discharged ballast water 

Predicted environmental concentration (PEC) of Active Substances and Relevant Chemicals in 

discharged ballast water from ships can be estimated from direct measurements of chemicals in 

treated seawater or estimated indirectly by measuring the oxidant level in the treated water. 
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6.2.2.1 Residual oxidant level 

Remaining concentrations of free and total residual oxidants in the treated ballast water at 

discharge was measured with standard colorimetric methods (HACH-Lange: DPD method; 

SM 4500-Cl G, USEPA 330.5). Free residual oxidant (see Textbox 2) measured with this method 

includes hypochlorous acid, hypochlorite ions, hypobromous acid and hypobromite ion,and total 

residual oxidant includes also the halogenamines and other less effective oxidants with N-C link. 

Oxidant decay was monitored following treatment of seawater with water qualities corresponding 

to the requirements in the Guidelines (G8) (intermediate salinity) (Table 10, Figures 6 and 7). 

Three tests were carried out on 9 May 2007 with varying dosages of anolyte. Tests Nos. 2 and 3 

correspond to the dosage that is used in the full scale version. 

Table 8: Measured water qualities in treated seawater in 

small scale tests (35 m3/hr) from 9 May 2007. 

TSS mg/l DOC, mg/l POC, mg/l Test on 9 May Average Stdev Average Stdev Average Stdev 

Required level 

(G8) > 50 - > 5 - > 5 - 

Control water 58.10 0.36 8.17 0.06 10.57 0.15 

Treated water 64.37 0.4 9.10 0.0 11.23 0.35 

Test 9 May 2007

Salinity: 23.7 psu, Temp: 12C 

0

0,5

1

1,5

2

2,5

0:00:00 12:00:00 24:00:00 36:00:00 48:00:00 60:00:00

Time (hours)

Total chlorine mg/L

Test 1

Test 2

Test 3

Figure 6: Total oxidant decay after treatment of surface seawater with three levels of 

anolyte (test 1: 3 L/m3, 2: 6 L/m3, 3: 9 L/m3). 
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Test 9 May 2007

Salinity: 23.7 psu, Temp: 12C 

0

0,5

1

1,5

2

2,5

0:00:00 12:00:00 24:00:00 36:00:00 48:00:00 60:00:00

Time (hours)

Free chlorine mg/L

Test 1

Test 2

Test 3

Figure 7: Free oxidant decay after treatment of surface seawater with three levels of 

anolyte (test 1: 3 L/m3, 2: 6 L/m3, 3: 9 L/m3). 

Probably due to high content of organic matter, the concentration of both TRO and Free oxidant 

is not detectable after less than 24 hours. 

Results from similar tests carried out on 23 May 2007 are presented in Figure 8 and 9 with 

corresponding water quality data in Table 10. Tests T-4 and T-9 are with seawater spiked with 

organic matter and particles. Test N-1 is with natural seawater from the surface layer of the Oslo 

fjord with no addition of particles or organic matter. The normal concentrations of organic matter 

in the surface layer of the Oslo fjord correspond to relative clean harbour water. Salinity during 

test was 21.5 psu and temperature in influent water was 11.8oC. 

Table 9: Measured water qualities in treated seawater 

in small scale tests (35 m3

/hr) 23 May 2007. 

TSS mg/l DOC, mg/l POC, mg/l Test on 23 May Average Stdev Average Stdev Average Stdev 

Test T-4 and T-9 62.93 0.93 9.17 0.06 8.90 1.76 

Test N-1 4.87 0.90 2.13 0.06 0.23 0.06 

Test 23 May 2007

Salinity: 21.5 psu Temp: 11.8 C 

0,0

0,5

1,0

1,5

2,0

2,5

3,0

3,5

4,0

0:00:00 2:24:00 4:48:00 7:12:00 9:36:00 12:00:00 14:24:00 16:48:00 19:12:00 21:36:00 24:00:00

Time (hours)

Total available oxidant (mg Cl/L)

N-1

T-4

T-9

Figure 8: Total oxidant decay after treatment of surface seawater with varying water 

quality (also see Table 10). 
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Test 23 May 2007

Salinity: 21.5 psu Temp: 11.8 C 

0,0

0,5

1,0

1,5

2,0

2,5

3,0

0:00:00 2:24:00 4:48:00 7:12:00 9:36:00 12:00:00 14:24:00 16:48:00 19:12:00 21:36:00 24:00:00

Time (hours)

Free oxidant (mg Cl/L)

N-1

T-4

T-9

Figure 9: Free oxidant decay after oxidant treatment of surface seawater with varying 

water quality (also see Table 10). 

The results for T-4 and T-9 with ìG8-water qualityî follow the results from 9 May with rapid 

decay in less than 6 hours. In ìunpollutedî water (Test N-1) oxidants are detectable at low levels 

more than 24 hours.

6.2.2.2 Measured concentration of chemical components

In June 2007 a >200 m3

/h version of the OceanSaver Ballast Water Management System (OS 

BWMS) was installed and operated at the Solbergstrand test facility. A tank with more than 500 m3

of challenge water was prepared in accordance with the Guidelines (G8) for 2-32 psu water. 

More than 200 m3

 of the challenge water was treated in a ballasting operation of the OS BWMS 

(treated water), whilst >200 m3

 of the challenge water was pumped, using the same pump system, 

through a bypass of the BWMS (control water). More than 200 m3

 of each of treated water and 

control water was collected in separate tanks and samples were taken from each for analysis of 

certain oxidation by-products (Day 0: 20.06.2007). After 5 days of storage, >200 m3

 of the 

Treated water was treated in a deballasting operation whilst >200 m3

 of the Control water was 

pumped, using the same pump system as the OS BWMS, through a bypass of the system 

(deballasted Control water). More than 200 m3

 of each of deballasted Treated water and 

deballasted Control water was collected in separate tanks and samples were removed from each 

for analysis of certain oxidation by-products (Day 5: 25.06.2007). The results from the analysis 

can be found in Table 10. 

The results are likely to be highly dependent on the operational settings of the C2E unit in the OS 

BWMS and the ambient features of the treated ballast water. In the initial test in June 2007 the 

concentration of Active Substances was slightly higher (> 3 mg/L measured as Free chlorine) 

than it will be in normal operation (approx. 2 mg/L). More analyses have been and will be carried 

out of treated water in the land-based tests at Solbergstrand from August to October 2007. 
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Table 10: Analysis results of oxidation by-products from samples collected during an 

initial test of OS BWMS at Solbergstrand, June 2007 (NIVA 2007b). 

Chemical Name Control 

day 0 

Control 

day 5 

Test 

day 0 

Test 

day 5 

μg/l μg/l μg/l μg/l 

AOX 29 <500 386 1290 

EOX < 50 < 50 < 50 < 50 

2-monochlorophenol <0.100 <0.100 <0.100 <0.100 

3- monochlorophenol <0.100 <0.100 <0.100 <0.100 

4- monochlorophenol <0.100 <0.100 <0.100 <0.100 

2,3-dichlorophenol <0.100 <0.100 <0.100 <0.100 

2,4+2,5-dichlorophenol <0.200 <0.200 <0.200 <0.200 

2,6-dichlorophenol <0.100 <0.100 <0.100 <0.100 

3,4-dichlorophenol <0.100 <0.100 <0.100 <0.100 

3,5-dichlorophenol <0.100 <0.100 <0.100 <0.100 

2,3,4-trichlorophenol <0.100 <0.100 <0.100 <0.100 

2,3,5-trichlorophenol <0.100 <0.100 <0.100 <0.100 

2,3,6-trichlorophenol <0.100 <0.100 <0.100 <0.100 

2,4,5-trichlorophenol <0.100 <0.100 <0.100 <0.100 

2,4,6-trichlorophenol <0.100 <0.100 <0.100 <0.100 

3,4,5-trichlorophenol <0.100 <0.100 <0.100 <0.100 

2,3,4,5-tetrachlorophenol <0.100 <0.100 <0.100 <0.100 

2,3,4,6-tetrachlorophenol <0.100 <0.100 <0.100 <0.100 

2,3,5,6-tetrachlorophenol <0.100 <0.100 <0.100 <0.100 

pentachlorophenol <0.100 <0.100 <0.100 <0.100 

trichloromethane/chloroform <0.300 <0.300 <0.300 <0.300 

tribromomethane/bromoform <0.200 0.822 385 398 

Dibromochloromethane <0.100 <0.100 14.7 17.8 

Dichlorobromomethane <0.100 <0.100 0.297 0.337 

CCL4-V <0.05 <0.05 <0.05 <0.05 

CHBR3-V 0.03 0.29 s170 s170 

CHCL3-V <0.05 <0.05 <0.05 <0.05 

DBRCM-V <0.02 0.02 4.2 4.5 

DCBRM-V <0.05 <0.05 0.13 0.11 

TCE-V <0.3 <0.3 <0.3 <0.3 

TECE-V <0.05 <0.05 <0.05 <0.05 

TRCE-V <0.05 <0.05 1.5 1.4 

6.2.3 PEC ñ PNEC estimation 

The preliminary results based on available data from pre-tests with higher oxidant levels than in 

normal operation indicate that several of the chemicals in Table 6 may have a PEC: PNEC ratio 

larger than 1 in discharged treated ballast water. With a dilution factor around 100, the 

discharged ballast water will have PEC: PNEC below 1. 
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6.3 Ecotox testing of treated ballast water 

A full ecotox evaluation will be reported in the Final Approval application. Currently, limited 

information is available from these tests. 

6.3.1 Ecotox testing of similar systems

A toxicological study of the Active Substances and Relevant Chemicals produced in an 

electrolytic process comparable to the C2E unit in the OS BWMS has been performed by the 

Institute of Chemistry at Tallinn Technical University (Munter et al. 1999), for checking the 

presence of toxic disinfection by-products and to measure the acute toxicity of the anolyte. 

Toxicity tests with both medium (Free active chlorine ~350 mg/L) and strong (Free active 

chlorine ~500 mg/L) anolyte were used for 24-h acute toxicity tests of Daphnia magna according 

to Finnish Standard SFS 5062. No acute effects were found for the anolyte diluted 1:500 or more 

and no significant differences between the two anolyte qualities were observed. 

Another study performed by the same scientific team, investigated the chronic toxicity of the 

same anolyte, by performing a 21-day full-life cycle Daphnia magna test (Munter et al., 2000). 

Mortality and reproduction were measured. The chronic test was performed with medium 

(Cac~350 mg/L) and strong (Cac~500 mg/L) anolyte at the determined maximum effective 

concentrations of 1:500 and 1:1000, respectively. The study concluded that no chronic toxic 

effects could be observed. 

These two toxicological studies cannot be said to be perfectly corresponding to the toxicity of the 

anolyte of the OS BWMS, as the anolyte in the two studies have been produced from brine and 

not from seawater. However, the result of the toxicological studies can be used for giving the 

main frame for the toxicity of the OS BWMS. Both studies indicate low or no toxicity if Active 

Substance is diluted to concentrations around 1 mg/L (Free chlorine) in treated water. 

The concentration of total residual oxidant in the anolyte produced in the C2E unit of OS BWMS 

is between 800 and 1000 mg/L. The theoretical calculated dosage of Active Substance measured 

as total residual oxidant in the OS BWMS is approximately 4-5 mg/L. Due to initial oxidant 

decay measured concentrations of total and free residual oxidant are around 1.5 and 2.5 in treated 

ballast water. After 24 hours, the concentration in polluted seawater is not detectable. In 

unpolluted coastal water, oxidants may be detectable 48 hours after treatment. 

6.3.2 Initial ecotox testing of ballast water treated with OS BWMS

Four ecotox test reports from NIVA of treated ballast water are available from the pre-test of the 

OS BWMS 20 June 2007 and one test report from the ordinary full-scale land-based G8 tests. 

Samples taken immediately after treatment with the C2E unit (Day 0 tests) have both acute and 

chronic toxicity. Samples from discharged ballast water (Day 5 test) have either low or no acute 

toxicity and must be diluted 1:1 for no chronic toxicity. 

Full toxicity assessment will be provided for the Final Approval. 
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7 RISK ASSESSMENT 

7.1 Risk to safety of ship 

Ships ballast water systems and, in particular, ballast water tanks are in many ways critical to the 

integrity of the ship simply because failure may cause flooding. 

Additional technologies and components installed on board ships may pose a threat to the general 

safety due to: 

- the characteristics of the actual technology installed; and 

- potential diversion of focus as officers and crew, already heavily loaded with 

various work-tasks, have to spend time on additional systems. 

The OS BWMS is developed in close encounter with the shipping industry by well experienced 

institutions well aware of the constraints, risks, but also the possibilities, as relevant in this 

context to the shipping industry. Safety has been the main priority in this work. Consequently, 

the product includes only well established and recognized components known from shipboard 

use wherever possible. All components and systems particular to the OS BWMS have been 

developed with safety in mind and in accordance with all relevant requirements. 

The system is fully automatic. Ballast operations will be carried out conventionally by the crew, 

thus not requiring level settings or other pre-actions. Further, maintenance requirements are 

integrated with the periodic survey programmes as required and with the vessels overall 

maintenance system. 

7.1.1 Ballast water tanks 

The structural integrity of a vessel is susceptible to corrosion and is widely recognized, e.g. the 

new IMO CPS (Coating Performance Standard), which requires particular corrosion protection in 

ballast water tanks. 

By treating ballast water prior to entering ballast tanks, the conventional corrosivity and/ or 

effects on any corrosion preventive systems will be affected in some way. OceanSaver has 

carried out extensive research and tests associated to the potential impacts its treatment may 

have. The OS BWMS creates a deficiency in available oxygen in the water when stored in the 

tanks and, consequently, oxidation of steel or coatings is reduced. The effects of this have been 

verified both by full-scale studies as well as by laboratory studies. 

The addition of the C2E disinfection introduces oxidants to the water in the tanks for a period of 

time. Because of the characteristics of the process, (short half-life and low concentration in a 

hypoxic environment), it does not incur on the positive effects the reduced level of oxygen has, 

as it is used in low concentrations. 

Results from independent full-scale testing suggest that the OS BWMS largely eliminates 

potential creep corrosion in ballast tanks. These assessments also conclude that the OS BWMS is 

fully compliant with the IMO CPS. 
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7.1.2 Ballast water pipe systems 

All piping that is particular for the OS BWMS is designed as a ìby-passî of a conventional 

ballast water system. This provides the vessel with redundancy and represents an additional 

safety feature. It should be noted that the OS BWMS monitoring system will log and report any 

by-pass operations. The OS BWMSís internal piping (between OS components) may either be 

made from conventional steel piping or from elastomeric-materials. The latter is a particular 

development of OceanSaver based on the use or armoured rubber tubing. This product has 

undergone severe testing and is approved for the use in all relevant dangerous areas (ex-areas). 

The elastomeric-material is particularly appropriate for retro-fittings. 

7.2 Risk to human health

The Active Substances and Relevant Chemicals produced in the OS BWMS not only pose an 

ecotoxic effect, they can also be toxic to humans. 

7.2.1 General 

The liquid solution produced by the C2E unit is non-toxic in nature but contains chemical 

formulations that can be mildly irritating to eyes, skin and digestive tract. 

In many electrochemical processes involving saline water, hydrogen gas may be formed. In the 

case of this particular application (electrodialysis), the actual electrochemical process takes place 

in a pressurized closed circuit. Any gas generated is compressed and partly re-dissolved into the 

flow. When the solution is re-injected into the main flow, this process is further enhanced by 

dilution. There is no release of any produced gas from the process to the atmosphere (vicinity) of 

the unit. The unit is, however, ventilated both as a safety precaution in case of leakage but also 

due to cooling purposes. Integrated gas detectors will detect any gas leakage. In the case of gas 

detection or pressure loss in the pressurized system, the electrical supply will be disconnected 

automatically and, thus, the system will shut down. 

The system is further protected by limiting the electrical supply to the electrodialytic cell as a 

function of its flow capacity making it impossible to build up explosive atmospheres 

(concentrations above 4% Hydrogen). Note also that the tanks when filled are also inerted due to 

the nitrogen supersaturation feature. 

As the C2E system produces the C2E disinfectant on demand in a pressurized enclosed circuit, 

there are no handling or storage issues. There are safety measures built into the system in case of 

failure causing leakage and thus the potential exposure to humans. In case of leakage, the system 

will automatically shut down. 

7.2.2 Precautions to be observed at all times

.1 Working Area: The area where the solution is being produced (the C2E unit) is 

required to be properly ventilated. The unit itself has an enclosed ventilation loop. 

The space in which the unit is installed should preferably have mechanical exhaust 

ventilation. During the production of activated solutions the exhaust air is warm 

and, therefore, a proper location should be provided. The temperature rise of the 

power supply is approximately 60o

C above ambient air. Venting to a large and 

well-ventilated place is desirable. Overheating will cause system auto-stop 

function to be activated. 
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.2 Engineering control procedures: Documented process and safety controls 

should be followed. 

.3 Dangerous voltage: Refer internal servicing of the C2E unit to qualified service 

personnel. To prevent electric shock or fire hazard, remove the power cords from 

the AC supply prior to connecting or disconnecting any signal lead, prior to 

replacing fuse, and prior to altering the set-up of the unit. 

.4 The C2E unit must be earthed: Earthed equipment is required for safety by 

regulations. In no event shall the manufacturer be liable for consequential or 

special damages to persons and/or objects due to failure to observe this safety rule. 

7.2.3 Hazards identification

The C2E solution is classified as non-dangerous (88/279/EWG) but may cause irritation to the eyes, 

sensitive skin and throat: 

.1 Health effects ñ skin: Exposure may cause irritation to sensitive skin or open 

wounds; 

.2 Health effects ñ eyes: The solution may cause irritation to the eyes; and 

.3 Health effects ñ ingestion: Swallowing of the solution may cause irritation to the 

throat and digestive tract. 

Conventional personal protective equipment (PPE) is considered adequate in order to protect against 

accidental exposure (i.e. gloves, and goggles). 

In case of ventilation breakdown or leakage, there is a risk of vapour or fumes to be released. These 

fumes may cause dizziness and nausea and inhalation should be avoided. 

The C2E solution does not react with other materials, therefore, it is stable and may be stored in 

sealed plastic containers. 

Where the C2E unit is operated, the following equipment should be available: 

.1 Hand protection: Protective gloves should be available; 

.2 Eye and facial protection: No requirements; 

.3 Inhalation: Respiratory protection should be available; and 

.4 Body protection: Normal industrial work wear should be available. 

7.2.4 Emergency measures 

In the case of an emergency, the system will shut down and the electrical supply is disconnected. 

The production of the C2E disinfectant will stop immediately. 

In the case of leakage, the quantity to enter the space is limited to the quantity in the actual cell. 

The liquid does not pose a fire hazard as it is not flammable. It is further biodegradable. The 

space contaminated by the liquid may be cleaned by conventional means. 
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7.2.5 Emergency first aid 

In the case of first aid emergency, the following procedures should be followed: 

.1 Eye contact: Where irritation occurs, flush with cool fresh water; 

.2 Skin Contact: Where irritation occurs, wash the skin with soap and warm water; 

.3 Ingestion: Drink cool fresh water to flush through and dilute; and 

.4 Inhalation: Move to fresh air. If dizziness and nausea persist seek medical 

attention. 

7.3 Risk to the aquatic environment

A study carried out by DNV (2007) investigated the dilution of six typical scenarios of ballast 

water discharge in a harbour recipient. A total ballast water volume of 50,000 m3

 is assumed 

discharged at a rate of 6,000 m3

/h. A typical harbour depth of 20 m is assumed. 

The discharge velocity is assumed to be just less than 4 m/s. A discharge pipe diameter of 750 

gives a velocity of 3.77 m/s. The discharge of water is assumed to occur at 8 m depth. This may 

be assumed to be a ìworst case scenarioî compared to a surface discharge, in that a surface 

discharge may experience more turbulent mixing. 

The initial mixing of the discharge in the recipient is modelled using Visual Plumes. This is an 

industry-standard tool provided by the US EPA, see www.epa.gov/ceampubl/swater/vplume/. 

A range of 6 scenarios are defined, combining 2 cases of longshore currents with 3 cases of 

density difference between discharge and recipient, thereby investigating the effect of density 

and currents on the extent of the plume: 

.1 no density difference, no current 

.2 no density difference, transverse current 

.3 brackish recipient, no current 

.4 brackish recipient, transverse current 

.5 brackish ballast, no current 

.6 brackish ballast, transverse current 

A near-zone of 300 m along the quay and 200 m from the ship side is defined. The total volume 

of this zone is 1,200,000 m3

. Therefore, excluding the effect of initial momentum and longshore 

currents, the discharge will be diluted >20 times within this zone. 

The boundary defining the near-zone has a flux area of 14,000 m2

. The flux of discharged ballast 

water through this boundary, again excluding the effect of initial momentum and longshore 

currents, is 0.42 m/h. Therefore, excluding the effect of initial momentum and longshore 

currents, it can be said that the discharge will be diluted >20 times within the 300 x 200 m 

near-zone to the discharge point, and that the flux of ballast water out of this zone is low. 

The initial mixing of ballast water gives a dilution of more than 20 x within 50 m of discharge. 

This is supported by general considerations of volumes and discharge rates, which find that 
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excluding the mixing effects of the initial momentum, and any longshore currents, a 20 x dilution 

is achieved in a 300 x 200 m near zone. The harbour current pattern will affect the influence zone 

to a great extent. Tidal currents and river flows can in many cases be expected to stretch the 

influence zone downstream and upstream. 

With these calculated initial dilutions available data indicate no significant environmental risk 

from discharged ballast water treated with the OS BWMS. 

More detailed simulations of yearly discharges to model ports will be provided for the Final 

Approval. 

8 REFERENCES 

Anon., 1999. Report on the test of the Anolyte produced by the unit Envirolyte, Trapido, 

Veressinina, Ahelik, Institute of Chemistry at Tallinn Technical University, Department of 

Environmental Chemistry and Technology, 1999. 

Anon., 2006. Cover story. New technology combats deadly microbes. The Clinical Services 

Journal, 5 (4), p. 7, July 2006. 

Applegate, VC., Howell JH, Hall Jr. AE., Smith M.A., 1957. Toxicity of 4,346 Chemichals to 

Larval Lampreys and Fishes. Spec.Sci.Rep.Fish.No.207, Fish Wildl.Serv. U.S.D.I.Washington, 

D.C.:157 p. 

Atkinson, L.P., 1973. Effect of air bubble solution on the air-sea gas exchange. J. Geophysical 

Research, 78 (6): 962-968. 

Behrends, B., 2006. The use of hydrodynamic cavitation for ballast water treatment in light of the 

provisions under Regulation D-3. paragraph 2 of the Ballast Water Management Convention 

(IMO, 2004). Theoretical study for MetaFIL AS. 

Behrends, B., A. Wick and T. Harder, 2007. ìPre-assessment of the impact of hydrodynamic 

cavitation on the chemical and biological properties of ballast waterî. Institute for Chemistry and 

Biology of the Marine Environment (ICBM) at the Carl von Ossietzky University in Oldenburg, 

Germany. 15.01.2007. 

Betzer, N., Kott, Y., 1969. Effect of Halogens on Algae-II. Cladophora sp. Water Res. 3(4):257-264. 

Boccafusco, RJ, Ells, SJ, LeBlanc, G.A. 1981. Acute toxicity of priority pollutants to bluegill 

(Lepomis macrochirus). Bull. Environ. Contam. Toxicol. 26: 446-452. 

Borzelleca JF & Carchman RA (1982) Effects of selected organic drinking water contaminants 

on male reproduction. Research Triangle Park; NC, US Environmental Protection Agency 

(EPA 600/1-82-009; NTIS PB82-259847; Contract No. R804290) [cited in IPCS, 2000]. 

Bull RJ et al. 1985. Evaluation of mutagenic and carcinogenic properties of brominated and chlorinated 

acetonitriles: by-products of chlorination. Fundamental and Applied Toxicology 5:1065-1074. 
MEPC 57/2/6 

ANNEX 

Page 72 

I:\MEPC\57\2-6.doc 

Broderius, SJ., Kahl, MD., Hoglund, MD., 1995. Use of Joint Toxic Response to Define the 

Primary Mode of Toxic Action for Diverse Industrial Organic Chemicals. Environ. Toxicol. 

Chem. 14(9):1591-1605 (Author Communication Used). 

Brown, J., A. Colling, D. Park, J. Phillips, D. Rothery and J. Wright, 1989. Seawater: Itís 

composition, properties and behaviour. Pergamon Press. 1989. 164 pp. 

Casillas, E., Myers, MS., 1989. Effect of Bromobenzene and 0-Bromophenol on Kidney and 

Liver of English Sole (Parophrys vetulus). Comp. Biochem. Physiol. C 93(1):43-48. 

CEFIC 2002. Hydrogen Peroxide: 28-day Inhalation Study in Rats. CTL/MR0211/Technical 

Toxicology/Report. Central Toxicology Laboratory, Alderley Park Macclesfield. CEFIC 

Peroxygen Sector Group. 

Charbonneau M et al. 1989. Involvement of reversible binding to alpha 2u-microglobulin in 1,4-

dichlorobenzene-induced nephrotoxicity. Toxicology and Applied Pharmacology 99:122-132. 

Chemical Properties Created by CCOHS (Canadian Center for Occupied Health and Safety). 

Christian MS et al. 2001. Oral (drinking water) developmental toxicity studies of 

bromodichloromethane in rats and rabbits. International Journal of Toxicology 20:225-237. 

Chu I et al. 1980. The acute toxicity of four trihalomethanes in male and female rats. Toxicology 

and Applied Pharmacology 52:351-353. 

Coler RA, Asbury, C. 1980. Acute toxicity of dissolved Ozone to eggs and larvae of selected 

freshwater fish species. Ozone Sci Eng. 2:177. 

Daniel FB et al. 1986. Genotoxic properties of haloacetonitriles: Drinking water by-products of 

chlorine disinfection. Fundamental and Applied Toxicology 6:447-453. 

De Angelo AB et al. 2002. The induction of aberrant crypt foci (ACF) in the colons of rats by 

trihalomethanes administered in the drinking water. Cancer Letters 187:25-31. 

Dragsund, E., A. Mjelde and Aa.B. Andersen, 2002. Ballast water treatment by nitrogen 

supersaturation. DNV Report 2003-1066. 30 pp. + appendices. 

DSBG/BCL 1985 b. Primary skin irritation stydy in rabbits. Unpublished study of Dead Sea 

Bromine Group 7BromineCompounds Ltd [cited in IUCLID, 2003]. 

DSBG/BCL 1997 b. Acute eye irritation test in the rabbit. Unpublished study of dead Sea 

Bromine Group / Bromine Compounds Ltd [cited in IUCLID, 2003]. 

DSBG/BCL 2002. Micronucleus test in bone marrow cells of the mouse with tribromophenol.

Unpublished study of Daed Sea Bromine Group / Bromie Compounds Ltd [Cited in IUCLID, 2003]. 

Eidnes, G. & K. Aareskjold, 1992. LNG-terminal at Slettnes. EIA of cooling water discharges to 

sea. SINTEF Report STF60 F92041. (In Norwegian). 
MEPC 57/2/6 

ANNEX 

Page 73 

I:\MEPC\57\2-6.doc 

Eloranta, V., 1982. Effect of the Slimecide Fennosan F50 on Algal Growth in Different Test 

Media. Pap. Puu 3:129-135. 

Erickson, SJ, Hawkins, CE, 1980. Effects of Halogenated Organic Compounds on Photosyntesis 

in Estuarine Phytoplankton. Bull. Environ. Contam. Toxicol. 24(6):910-915. 

Erickson, S.J., Freeman, A.E., 1978. Toxicity Screening of Fifteen Chlorinated and Brominated 

Compounds Using Four Species of Marine Phytoplankton. In: Jolley, R.L., Gorchev, H., 

Hamilton, D.H. (Eds.), Water Chlorination: Environmental Impact and Health Effects, Ann 

Arbor Sci. Pupl., Ann. Arbor, MI 2:307-310. 

Farkas, L., M. Lewin, and R. Bloch, 1988. The Reaction between Hypochlorites and Bromides. J. 

Amer. Chem. Soc., 71. 

FMC Corporation 1997. Hydrogen Peroxide 13-week Drinking water Study with 6-week 

Recovery Period in C57BL/6NCrlBR Mice. FMC Study No. 195-2039. FMC corporation 

Toxicology Laboratory, Princeton, NJ. 

Folsom, Dale W., Jody A. Jones and Robert F. Olfenbuttel, 1994. Evaluation of an 

Electrodialytic Process for Purification of Hexavalent Chromium Solutions. Project Summary. 

Research and Development, EPA/600/SR-94/071. 

Geiger, DL., Northcott, CE., Call, DJ., Brooke, LT., 1985. Acute Toxicities of Organic 

Chemicals to Fathead Monnows (Pimephales promelas), Volume 2. Ctr. For Lake Superior 

Environ. Stud., Univ. of Wisconsin-Superior, Superior, WI :326 p. 

Gersdorff, WA., Smith, LE. 1940. Effect of Introduction of the Halogens into the Phenol 

Molecule on Toxicity to Goldfish. II. Bromophenols. Am. J. Pharm. 112:316-322. 

Gibson, CI., Tone, FC., Wilkinson, p., Blaylock, JW., Shirmer, RE., 1981. Toxicity, 

Bioaccumulation and Depuration of Bromoform in Five Marine Species. Pacific Northwest Lab., 

Richland, WA:40 p. (U.S.NTIS NUREG/CR-1297). 

Gunnison AF, Weideman PA, Sobo M. 1992. Enhanced inflammatory response to acute Ozone 

exposure in rats during pregnancy and lacation. Fundam Appl Toxicol (19) 607-612. 

Harp D.L. 2002. Current Technology of Chlorine Analysis for Water and Wastewater. Technical Information 

Series ñ Booklet No.17. Hach Company. www.hach.com/fmmimghach?/CODE:L70191473|1//true. 

Hayes JR, Condie, LW, Borzelleca JF 1986. Toxicology of haloacetonitriles. Environmental 

Health Perspectives 69:183-202. 

Heagle, AS, Philbeck, RB, Knott, WM. 1979. Thresholds for injury, growth and yield loss caused 

by Ozone on field corn hybrids. Phytopathology 69(1): 21-26. 

Hose, JE., Fiore Di, D., Parker, HS., Sciarrotta, T., 1989. Toxicity of Chlorine Dioxide to Early 

Life Stage of Marine Organisms. Bull.Environ.Contam.Toxicol. 42(3):315-319. 

Huang, JC. Gloyna, EF., 1968. Effect of Organic Compounds om Photosynthetic Oxygenation-I. 

Chlorophyll Destryction and Suppression of Photosynthetic Oxygen Production. Water Res. 2:347-366. 
MEPC 57/2/6 

ANNEX 

Page 74 

I:\MEPC\57\2-6.doc 

Ichikawa, SY., Wakao, SY., Fukuyo, Y., 1993. Hydrogen Peroxide as an Extermination Agent 

Against Cysts of Red Tide and Toxic Dinoflagellates. In: Smayda, TJ. And Shimizu, Y. (Eds.), 

Phytoplankton Blooms in the Sea, Elsevier Sci.Publ., Amsterdam, Netherlands 3:133-138. 

Ishidate M et al. 1982. Studies on the mutagenicity of low boiling organohalogen compounds.

Unpublished interagency report to the National Institute of Hygienic Sciences, Tokyo Medical 

and Dental University, Tokyo. 

IPCS 2000. Disinfectants and disinfectant by-products. Geneva, World Health Organization, 

International Programme on Chemical Safety (Environmental Health Criteria 216). 

IRDC 1973. Acute toxicity studies in rats and rabbits. Mattawan, MI, International Research 

Development Corporation (Report No. EPA/OTS 86-900000302; NTIS/OTS 0523294; submitted 

to US EPA with test data and cover letter by Great Lakes Chemical Corporation, West Lafayette, 

IN, March 1990). 

IRDC 1974 a. Acute dermal toxicity in male and female albino rabbits. Mattawan, MI, 

International Research Development Corporation (Report No. EPA/OTS 0523298; submitted to 

US EPA with test data and cover letter by Great Lakes Chemical Corporation, West Lafayette, 

IN, March 1990). 

IRDC 1978 b. Pilot teratology study in rats. Mattawan, MI, International Research Development 

Corporation (Report No. EPA/OTS 86-900000316; NTIS/OTS 0523308; submitted to US EPA with 

test data and cover letter by Great Lakes Chemical Corporation, West Lafayette; IN, March 1990). 

Ito R, Kawamura H, Chang HS, Toida S, Matsuura S, Hidano T, Nakai S, Inayoshi Y, Matsuura 

M, Akuzawa K 1976. Oral safety on hydrogen peroxide, acute and subacute toxicity. J Med Soc 

Toho (23) 531-537. 

Ito A, Naito M and Watanabe H 1981. Implication of chemical carcinogenesis in the experimental 

animal. Ann. Rep. og Hiroshima Univ Res. Inst. Nuclear Medicine and Biology 22, 147-158. 

Ito A, Watanabe H, Naito Y 1981 b. Prevalence of Gastric Erosions and Duodenal Tumors with a 

continous Oral Administration og Hydrogen Peroxide in C57BL/6J Mice. Study Report. Research 

Institute for Nuclear Medicine and Biology, Department of Cancer Research, Hiroshima. 

Jelmert, A., 2001. Ballast Water Treatment by Gas Supersaturation. 1st International Ballast 

Water Treatment R&D Symposium. IMO London 26-27 March 2001. 

Jenner, H.A., J.W. Whitehouse, C.J.L. Taylor & M. Khalanski, 1998. Cooling water management 

in European power stations. Hydroecologie Applique, 10 (1-2): pp. 1-225. 

Kavlock R, Daston G, Grabowski CT 1979. Studies on the developmental toxicity of Ozone. I. 

Prenatal effects. Toxicol Appl Pharmacol (48) 19-28. 

Kavlock RJ, Meyer E, Grabowski CT 1980. Studies on the developmental toxicity of Ozone: 

postnatal effects. Toxicol Lett (5) 3-9. 
MEPC 57/2/6 

ANNEX 

Page 75 

I:\MEPC\57\2-6.doc 

Klein Szanto AJP, Slaga TJ 1982. Effects of peroxides on rodent skin: Epidermal hyperplasia and 

tumor promotion. J. Invest. Dermatol. (79) 30-34. 

Kondrashov VA 1977. Evaluation of the toxicity of hydrogen peroxide vapors for inhalation and 

percutaneous exposures. Gig. Tr. Prof. Zabol. (21) 22-25 . 

Kott, Y., Edlis, J., 1969. Effects of Halogens on Algae-I. Chlorella sorokiniana. Water Res. 3(4): 251-256. 

Kuhn, R., 1988. Schadstoffwirkungen von Umweltchemikalien im Daphnien-Reproduktions-Test 

als Grundlage fr die Bewertung der Umweltgefhrlichkeit in Aquatischen Sys. 

Forschungsbericht 10603052 Mrz (OECDG Data File). 

Kuhn, R., Pattard, M., Pernak, K-D., Winter, A., 1989. Results of the Harmful Effects of Water 

Pollutants to Daphnia magna in the 21 Day Reproduction Test. Water Res. 23(4):501-510 

(OECDG Data File). 

Kuhn, R., Pattard, M., 1990. Results of the Harmful Effects of Water Pollutants to Green Algae 

(Scenedesmus subspiciatus) in the Cell Multiplication Inhibition Test. Water Res. 24(1):31-38 

(OECDG Data File). 

LeBlanc, GA 1980, Acute toxicity of priority pollutants to water flea (Daphnia magna). Bull. 

Environ. Cintam. Toxicol. 24:684-691. 

Le Curieux F et al. 1995. Study of the genotoxic activity of six halogenated acetonitriles, 

using the SOS chromotest, the Ames fluctuation test and the newt micronucleus test. 

Mutation Research 341(4): 289-302. 

Lewis RJ, Sweet, DV, 1984. Registry of toxic effects of chemical substances. National Institute 

of Occupational Safety and Health. No. 83-107-4. 

Loeb, HA., Kelly, WH., 1963. Achute Oral Toxicity of 1,496 Chemicals Force-red to Carp. 

U.S.Fish.Wildl.Serv., Sp.Sci.Rep. ñFish.No.471, Washington, D.C. :124 p. 

Lyubimov AV, Babin W, Kartashov AL 1998. Developmental neurotoxicity of 2,4,6-

tribromophenol in Wistar rats. Neurotoxicology, 19(2):303-312. 

Mayes, M., Blanchard, FA, Hopkins, DL, Takahashi, IT, 1985. Static Acute Toxicity of 

Dibromonitrilopropionamide and Selected Degradation Products to the Fathead Minnow 

(Pimephales promales Rafinesque). Environ. Toxicol.Chem. 4(6):823-830. 

McDonnell WF, Kehrl HW, Abdul-Salaam S, Ives PJ, Folinsbee LJ, Devlin RB. 1991. 

Respiratory response of humans exposed to low levels of Ozone for 6.6 hours . Arch Environ 

Health (46 (3):145-150. 

MEPC 56/2, para. 2.3.6.2, GESAMP-BWWG. 

MEPC 56/2, para. 2.3.7.2, GESAMP- BWWG. 

MEPC 56/2, para. 2.3.1.2, GESAMP- BWWG, Daniel et al 1990. 
MEPC 57/2/6 

ANNEX 

Page 76 

I:\MEPC\57\2-6.doc 

MEPC 56/2, para. 2.3.5.2 GESAMP-BWWG. 

MITI 1992. Biodegradation and bioaccumulation data of existing chemicals based the CSCL 

Japan. Compild under the Safety Division Basic Industies Buerau Ministry of International 

Trade & Industry, Japan. Edited by Chemicals Inspection & Testing Institute, Japan. 

Moraes EC, Keyse SM, Tyrrell RM 1990. Mutagenesis by hydrogen peroxide treatment of 

mammalian cells: a molecular analysis. Carcinogenesis (11) 283-293. 

Morimoto K & Koizumi A 1983. Trihalomethanes induce sister chromatid exchanges in human 

lymphocytes in vitro and mouse bone marrow cells in vivo. Environmental Research 32:72-79. 

Nakamura S, Oda Y, Shimada T, Oki I, Sugimoto K 1987. SOS-inducing activity of chemical 

carcinogens and mutagens in Salmonella typhimurium TA1535/pSK1002: Examination with 151 

chemicals. Mutat. Res. 192, 239-246. 

NIVA 2007. Active compounds produced by the C2E unit. NIVA Technical Note, July 2007. 

NTP (1985) Toxicology and carcinpogenesis studies of chlorodibromomethane (CAS No. 124-48-1) 

in F344/N rats and B6C3F1 mice (gavage studies). Research Triangle Park, NC, US Department 

of Health and Human Services, National Toxicology Program (NTP TR 282). 

NTP (1987) Toxicology and carcinogenesis studies of bromodichloromethane (CAS No. 75-27-4) 

in F344/N rats and B6C3F1 mice (gavage studies). Research Triangle Park, NC, US Department 

of Health and Human Services, National Toxicology Program (NTP TR 282). 

NTP (2000c) 14-day toxicity study of dibromoacetonitrile administration in dosed water to 

Fisher-344 rats. Study report submitted to the National Toxicology Program, National Institute 

of Environmental Health Sciences, National Institutes of Health, Research Triangle Park, NC, 

December 2000. 

NTP (2001b) Subchronic toxicity of bibromoacetonitrile administered in dosed water to Fisher 344 rats. 

Study report submitted to the National Toxicology Program, National Institute of Environmental 

Health Sciences, National Institutes of Health, Research Triangle Park, NC, July 2001. 

NTP 2002 a. Abstracts from subacute and subchronic studies of dibromoacetonitrile (DBAN) on 

Fisher-344 rats and B6CF1 mice, and update on test status. Research Triangle Park, NC, 

National Institutes of Health, National Institute of Environmental Health Sciences, National 

Toxicology Program. Available on http://ntp-server.niehs.nih.gov/.

NTP 2002 b. Pathology Working GroupChairpersonsís report. 13 week study of 

bromochloracetic acid (C96019), dibromoacetonitriles (C96015), and bromodichloroacetic acid 

(C096014) administered by dosed water in male and female B6C3F1 mice and male and 

female F344 rats. Research Triangle Park, NC, National Institutes of Health, National Institute of 

Environmental Health Sciences, National Toxicology Program, February 2002. 

Paller MH, Heidinger RC. 1979. Toxicity of Ozone to bluegill. J. Environ. Sci. & Health 14A:169. 
MEPC 57/2/6 

ANNEX 

Page 77 

I:\MEPC\57\2-6.doc 

Phipps, GL., Holcombe, GW., Fiandt, JT., 1981. Acute Toxicity of Phenol and Substituted 

Phenols to the Fathead Minnow. Bull. Environ. Contam. Toxicol. 26(5):585-593 (Author 

Communication Used) (OECDG Data File). 

Portmann, JE., Wilson, KW., 1971. The Toxicity of 140 Substances to the Brown Shrimp and 

Other Marine Animals. Shellfish Information Leaflet no.22 (2nd Ed.), Ministry of 

Agric.Fish.Food, Fish.Lab.Burnham-on-Crouch, Essex, and Fish Exp. Station Conway, North 

Wales :12 p. 

Punte CL, Saunders LZ, Krackow EH 1953. The Inhalation Toxicity of Aeroslos of 90% 

Hydrogen Peroxide. Chemical Corps Medical laboratories Research Report No. 189. Army 

Chemical Center, MD. 

Prilutsky, V.I., V.M. Bakhir, N.Yu. Shomovskaya. Disinfectant agents: efficacy, safety, ecology, 

Ekologiya i Promyshlennost Rossii . ñ 2003. ñ October ñ pp. 31-34. 

Prise KM, Davies S, Michael BD 1989. Cell killing and DNA damage in Chineese hamster V79 

cells treated with hydrogen peroxide. Int. J. Radiat. Biol. (55) 583-192. 

Punte CL, Saunders LZ, Krackow EH 1953. The InhalationToxicity of Aerosols of 90% 

Hydrogen Peroxide. Chemical Corps Medical laboratories Research Report No. 189. Army 

Chemical Center, MD. 

Renfro, W. C., 1963. Gas-bubble mortality of fishes in Galveston Bay, Texas. Trans. Am. Fish. 

Soc. 92: 320-322. 

Sasaki K, Kusakabe H, Takahashi T, Hashimoto K 1999. In vitro chromosomal aberration test 

of 2,4,6-tribromophenol on cultured Chinese hamster cells. Kanagawa Ministry of Health & 

Environmental Chemicals No. 7; http://wwwdb.mhlw.go.jp/ginc/dbfile1/paper/paper118-79-

6f.html) (in Japanese). 

Selleck, et al., 1976. Optimization of Chlorine Application Procedures and Evaluation of 

Chlorine Monitoring Techniques. Univ. of California Publication No. UCB-ENG-4180, 

Berkeley, CA. 

Smith MK, George EL, Zenick H, Manson JM, Stober JA 1987. Developmental toxicity of 

halogenated acetonitriles: drinking water by-products of chlorine disinfection. Toxicology. 46:83-93. 

Spector DM, Lippmann M, Thurston GD, Lioy PJ, Stecko J, OíConnor G 1988. Effects of 

ambient Ozone on respiratory function in healthy adults exercising outdoors. Am Rev Respir Dis 

(138) 821-828. 

Spektor A, Garner WH 1981. Hydrogen peroxide and human cataract. Exp. Eye Res. (33) 670-681. 

SRI International 1980. Hydrogen Peroxie. Microbial Mutagenesis Testing of Substances 

Compound Report: F76-017, Hydrogen Peroxide. Project LSU-6909. Dept. of Health, Education 

and Welfare FDA. SRI International. 

Stickney, A. P., 1968. Supersaturation of atmospheric gases in the coastal waters of the Gulf of 

Maine. Fishery Bulletin, 67 (1): 117- 123. 
MEPC 57/2/6 

ANNEX 

Page 78 

I:\MEPC\57\2-6.doc 

Stroud, B., H. Yang and Y. Li. 2001. Antimicrobial treatment of fresh-cut vegetables using 

electrochemically activated water. Presented at IFT 2001 Annual Meeting, June 23-27, 2001, 

New Orleans, LA. Paper No. 30B-29, pp 60 in: 2001 IFT Annual Meeting Book of Abstracts. 

Institute of Food Technologists, Chicago, IL. 

Sugam R. and Helz G.R. 1981. Chlorine speciation in seawater; a metastabile equilibrium model 

for ClI

 and BrI species. Chemosphere 10: 41-57. 

Swem, B., H. Yang and Y. Li. 2001. Effects of electrochemically activated water on inactivation 

of pathogens with biofilms in dipping treatment of fresh-cut vegetables. Presented at the Food 

Safety Consortium 2001 Annual Meeting, September 16-18, Ames, IA. Abstract in: Food Safety 

Consortium 2001 Annual MeetingóAgenda, Presentations, and Progress Reports. 

Tamburri, M.N, K. Wasson, Matsuda, M. 2001. Ballast Water Deoxygenation Can Prevent Species 

Introductions While Reducing Ship Corrosion. Biological Conservation, 103: pp. 331-341. 

 

Tanaka R, Yamada, R, Oba K, Iga T, Mikami S 1999. Combined repeat dose and 

reproductive/developmental toxicity screening test of 2,4,6-tribromophenol by oral 

administration in rats. Shizuoka, Japan Ministry of Health & Welfare, Biosafety 

Research centre (Toxicity Testing Reports of Environmental Chemicals 

No. http://wwwdb.mhlw.go.jp/ginc/dbfile1/paper/paper11879-6d.html) (in Japanese). 

Tooby, TE., Hursey, PA., Alabaster, JS., 1975. The Achute Toxicity of 102 Pesticides and 

Miscellaneous Substances to Fish. Chem.Ind.(Lond.) 21:523-523. 

Trapido, M., Veressinina, Y. and Ahelik, V, 1999. Report on the test of the Anolyte produced by 

the unit ENVIROLYTE. Report from Institute of Chemistry at Tallinn Technical University, 

Department of Environmental Chemistry and Technology. 9 pp. 

Trenel, J., Kuhn, R., 1982. Bewertung Wassergefahrdender Stoffe im Hinblick auf Lagerung und 

Transport Umweltforshungsplan des Bundesministers des Innern (OECDG Data File). 

US EPA (Iris). 

Yang, Z., Y. Li and M.F. Slavik. 1999. Antibacterial efficacy of electrochemically activated solution 

applied in inside/outside spraying and chilling processes. Journal of Food Science 64(3):469-472. 

Veninga TS 1967. Toxicity of Ozone in comparison with ionizing radiation. Strahlentherapie (134) 469-477. 

Ward, GS., Parrish, PR., Rigby, RA., 1981. Early Life Stage Toxicity Tests with a Saltwater 

Fish: Effects of Eight Chemicals on Survival, Growth, and Development of Sheepshead 

Minnows. J. Toxicol. Environ. Health 8(1-2):225-240. 

Wedemaier, GA et al 1979. Physiological and biochemical aspects of Ozone toxicity to rainbow 

trout (Salmo gairdneri) J. Fish Res Bd. Can 36. 605. 

Weiss, R. F., 1970. The solubility of nitrogen, oxygen and argon in water and seawater. DeepSea Research 17, 721ñ735. 
MEPC 57/2/6 

ANNEX 

Page 79 

I:\MEPC\57\2-6.doc 

Weitzman SA, Weitberg AB, Stossel TP, Schwartz J, Shklar G 1986. Effects of hydrogen 

peroxide on oral carcinogenesis in hamsters. J. Periodontol (57) 685-688. 

White, G. C., 1999. Handbook of chlorination and alternative disinfectant. 4th edition. John Wiley 

& Sons, Inc. 1569 pp. 

Wilson, T.R.S., 1975. Salinity and the major elements of seawater. In: Chemical oceanography, 

J.P. Riley & Skirrow (eds), Vol. 1, 365-413. London: Academic Press. 

Woodiwiss, FS., Fretwell, G., 1974. The Toxicities of Sewage Effluents, Industrial Discharges 

and Some Chemical Substances to Brown Trout (Salmo trutta) in the Trent River Authority Area, 

Water Pollut.Control 73:396-405. 

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