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INTERNATIONAL MARITIME ORGANIZATION

IMO 

E

MARINE ENVIRONMENT PROTECTION 

COMMITTEE 

57th session 

Agenda item 2 

MEPC 57/2/1

 7 September 2007

 Original: ENGLISH

HARMFUL AQUATIC ORGANISMS IN BALLAST WATER 

Application for Final Approval of a ballast water management system using 

Active Substances (Electro-Clean Electrolytic Disinfection) 

Submitted by the Republic of Korea 

SUMMARY

Executive summary: This document contains an application for Final Approval of a ballast 

water management system using Active Substances in accordance 

with the Procedure for approval of Ballast Water Management 

Systems that make use of Active Substances (G9) adopted by 

resolution MEPC.126(53) 

Action to be taken: Paragraph 5 

Related documents: MEPC 53/24, MEPC 53/24/Add.1, MEPC 54/2/3 and BWM.2/Circ.10 

Introduction

1 Ballast Water Management Systems which make use of Active Substances or 

preparations containing one or more Active Substances shall be approved by the Organization 

under the Regulation D-3.2 of the Ballast Water Management Convention. 

2 The Procedure for approval of Ballast Water Management Systems that make use of 

Active Substances (G9) contains the information that should be included into a proposal for 

approval and provisions for risk characterization and analysis. According to section 6 of the 

Procedure (G9), the Organization should evaluate the information provided in the application. 

3 According to BWM.2/Circ.10, a document on the proposal for approval containing all the 

non-confidential data related to the respective Ballast Water Management Systems that make use 

of Active Substance should be submitted to MEPC 56 or, if this is not possible, to 

MEPC 57 not later than 7 September 2007. 

4 Republic of Korea has verified the application dossier and believes it satisfies the data 

requirements of the Procedure (G9) adopted by the resolution MEPC.126(53). Therefore, the 

Republic of Korea submits the non-confidential part of the manufacturer’s 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-BWWG with the 

understanding of confidential treatment. 
MEPC 57/2/1 - 2 - 

I:\MEPC\57\2-1.doc 

Action requested of the Committee 

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

as appropriate. 

*** 
MEPC 57/2/1 

I:\MEPC\57\2-1.doc 

ANNEX 

INFORMATION ON 

ELECTRO-CLEAN BALLAST WATER MANAGEMENT SYSTEM 

1 Introduction

The Electro-Clean System (ECS), designed and manufactured by Techcross Inc., is the ballast 

water management system that has been engineered for the disinfection of micro-organisms that 

would otherwise be indigenous to the aquatic ecosystem. Ever since the achievement of the 

basic approval, the manufacturer has evaluated the system for its land-based tests with its test 

facilities and shipboard tests in accordance with G8 and G9 Guidelines and taking into account 

the recommendation of the GESAMP’s review. 

Through rigorous land-based and shipboard testing, the ECS is found to have the many positive 

attributes that make it a highly effective ballast water treatment system. Without the addition of 

any synthetic chemicals, with just the application of electric currents, hypochlorite 

(active substance) is generated in situ and disinfects the micro-organisms effectively. 

In addition to this, electric potential and OH radicals that do not leave any trace, generated 

during the electrolysis procedure also disinfect micro-organisms. Hypochlorite is highly 

reactive and easily degraded in seawater containing both organics and inorganics. The active 

substance used in the process of ECS and disinfection by-products do not cause any secondary 

pollution and is therefore not harmful to the aquatic environment. 

The ECS has the capability to control the level of active substances automatically, thus enabling 

the control of its disinfection efficacy to the level that is required in any given situation. 

After the initial installation of the ECS, it is unnecessary for any chemicals to be added to the 

system, providing a safe working environment for the crew. 

In March 2006, upon receiving the basic approval for the ECS, land-based tests have been 

conducted under the supervision of Korea Ocean Research and Development Institute (KORDI) 

from September 2006 until August 2007, all of which the results are in satisfaction 

with D-2 standard. Also, shipboard tests on the M/V STX Yokohama have been conducted 

from January 2007 until August 2007 and, under the supervision of KORDI, the ECS installed 

has been tested and the treated ballast water has proven to satisfy the D-2 standard. 

From March to August 2007, toxicity tests in accordance with the existing guidelines have been 

conducted to analyse the impact of treated ballast water on ecosystems of seawater and of 

brackish water. Corrosion tests have been conducted on the treated ballast water and the gases 

that may be produced during the operation of ECS have been monitored and analysed. With the 

use of the emission scenario, the environmental impact has been analysed when the treated 

ballast water was discharged at port. 

All the information was presented to the IMO technical reviews on ballast water management 

technologies during the development phase. The availability of the electrochemical treatment of 

ballast water was first introduced in document MEPC 53/2/31. The “Ballast Water Management 

System Electro-Clean” technology has been presented at MEPC 54, MEPC 55, MEPC 56, 

and BLG 11 for its developing and testing procedures. The system has also been presented at 

the Oceans ’06 Conference IEEE in Asia Pacific, Singapore, ICBWM 2006 in Singapore, 

and 2006 Lloyd’s List Conference on Ballast Water Management in London. 
MEPC 57/2/1 

ANNEX 

Page 2 

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The Active Substances are generated during the electrolysis process by ECS, when chloride ion 

in seawater is oxidized and converted into chlorine that is subsequently dissolved into water and 

is present in the form of OCl- and HOCl. These species have very high oxidation power and are 

highly reactive with most organic matter. The chemical compounds of reactive chlorine and 

other oxidants are called Total Residual Chlorine (TRC) or total residual oxidants (TRO). 

They have been recognized to destroy micro-organisms instantaneously. 

The total residual chlorine concentration is measured with a single spot spectrophotometric 

measurement using DPD reagent (total chlorine indicator) and is used for monitoring and 

calibration of the CLX online chlorine monitor (HF Scientific, Inc.). The CLX measures the 

TRC concentration in seawater by the DPD (N, N-Diethyl-P-Phenylenediamine) method. 

The concentration for Active Substances can be measured in terms of TRC. From biological 

efficacy tests, 10 mg/L of TRC is effective enough to disinfect micro-organisms in seawater 

containing various concentrations of suspended solids and organic substances, 

satisfying D-2 standards. From the results, the maximum applied concentration of TRC has 

been controlled at 10 mg/L, whereas 20~30 mg/L TRC concentration has been applied for the 

basic approval. Therefore the TRC concentration has been reduced from 30 mg/L to 10 mg/L. 

From the long-term land-based test results, the maximum TRC concentration of the effluent 

ballast water, after 5 days of storage, has been decreased to below 2 mg/L. 

2 Disinfection mechanisms by ECS 

During electrolysis of seawater in ECS, chlorine, Cl2 (g) is formed from oxidation of chloride 

ion and is dissolved into seawater as follows: 

Cl2 (g) Cl2 (aq) K = 6.2 x 10-2 (2-1) 

Cl2 (aq) then hydrolyzes, one of the chlorine atoms being oxidized to +1 and the other reduced 

to -1. This reaction is called disproportionation. The reaction is as follows: 

Cl2 (aq) + H2O HOCl + H+ + Cl-1 KH = 4 x 10-4 (2-2) 

From Equation (2-2), the hypochlorous acid, HOCl, is formed. The water becomes acidic. 

If the water is intentionally made acidic, the reaction will be driven to the left, producing more 

of the chlorine molecule. This condition will then produce more disinfecting power. Otherwise, 

HOCl further reacts to produce the following dissociation reaction: 

HOCl H+ + OCl- Ka = 10-7.5 (2-3) 

Using Equation (2-2), the distribution of Cl2 (aq) and HOCl can be calculated. Expressing in the 

form of equilibrium equation: 

KH = 4 x 10-4 = 

[ ( )]

[ ][ ][ ]

Cl2 aq

HOCl H Cl + −

 (2-4) 

Taking logarithms, rearranging and simplifying: 

[ )]

[ ( )] 2

HOCl

Cl aq = 10 {pK

H

-pH+Log[Cl-]} (2-5) 
MEPC 57/2/1 

ANNEX 

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Using Equation (2-3), let us calculate the distribution of HOCl and OCl-. Note that from 

previous result, HOCl predominates over Cl2 (aq) above pH4.0, Cl2 (aq) being practically zero. 

Thus above this pH, the distribution of the chlorine species will simply be for HOCl and OCl-

. 

Expressing Equation (2-3) in the form of equilibrium equation: 

Ka = 10-7.5

 = 

[ ]

[ ][ ]

HOCl

H OCl + −

 (2.6) 

Taking logarithms, rearranging and simplifying: 

[ ]

[ ]

HOCl

OCl −

 = 10 pH-7.5 (2.7) 

At exactly pH 7.5, the concentration of HOCl and OCl-

 are equal and above this pH, OClpredominates over all chlorine disinfectant species. 

The three species Cl2 (aq), HOCl, and OCl-

 are called total free chlorine. Although Cl2 (aq) is a 

stronger oxidizer than the other two, it is not really of much use, unless the water is very acidic. 

The OCl- and HOCl species are commonly referred to as free chlorine, which is extremely 

reactive with numerous components of the bacterial cell. HOCl can produce oxidation, 

hydrolysis and deamination reactions with a variety of chemical substrates, and produces 

physiological lesions that may affect several cellular processes. 

Chlorine was later found to have powerful effects on sulfhydryl groups of proteins 

(Knox et al., 1948) and to convert several amino acids by oxidation into a mixture of 

corresponding nitriles and aldehydes. The exact product of the reaction depends on chlorine 

concentration and pH (Dakin 1916, 1917; Wright 1936). Cytochromes, iron-sulfur proteins and 

nucleotides are highly vulnerable to oxidative degradation by HOCl, suggesting that chlorine 

causes physiological damage primarily to the bacterial cell membranes 

(Camper & McFeters, 1979; Haas & Engelbrecht, 1980; Albrich, McCarthy & Hurst, 1981). 

In addition, chlorination can kill microbes by disrupting metabolism and protein synthesis, or 

by modifying purine and pyrimidine bases and thus causing genetic defects 

(Haas & Engelbrecht, 1980). 

3 Description of Electro-Clean System 

3.1 System process 

3.1.1 Switchboard panel and multi-relay (HIMAP) 

The electric power is supplied to the rectifier, cooler, control units, the electrolysis module, and 

control systems. The multi-function relay monitors the conditions of the switchboard panel 

controlling it according to the directions of the control PC. 

The voltage and current of the DC power is automatically generated by a program that 

undergoes three steps. 
MEPC 57/2/1 

ANNEX 

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In the first step, the voltage and current shall be determined by manufacture settings, which are 

the values measured from the salinity sensor are supplied. In the second step, the initial voltage 

and current are automatically changed by the data programmed with the initial settings. In the 

third step, the TRC concentration in the ballast water is detected by the TRC sensor, and the 

data of residual chlorine concentration are sent to the control PC, which supplies the 

programmed voltage and current to the electrolysis module for the most effective disinfection. 

During inballasting, the Electro-Clean System continuously controls the voltage and current by 

sensing data for ECS operation. 

3.1.2 Rectifier and heat-exchanger 

The rectifier converts AC to DC to supply the appropriate quantity of DC power to the 

electrolysis module, and the cooler discharges heat generated from the rectifier. When the 

ballast pump is activated and the control PC sends operation signals, the Remote Terminal 

Unit (RTU) receives these signals and transfers them to the control PC. Then the control 

PC activates the cooler and rectifier supplying DC power to the electrolysis module. 

3.1.3 Electrolysis module 

The electrolysis module is the component that removes harmful living micro-organisms from 

the ballast water. Although there are variances depending on the properties of the ballast water, 

the water is disinfected by reacting within a very short time under a low voltage. The electricity 

is supplied from the switchboard panel and rectifier to the electrode of the electrolysis module. 

Disinfection begins when seawater flows into the electrode module and reaches the electrodes. 

Efficacy of disinfection depends on the conductivity, saline concentration, and electric current. 

The optimal conditions for disinfection according to the properties of the ballast water are 

received from the control PC. 

3.1.4 TRC control system 

3.1.4.1 System control overview 

Organisms in ballast water are disinfected mainly by electric potential difference by the 

ECS system and TRC that is the active substance material generated from electrolysis. 

Generation of the active substance TRC is controlled by water properties and the input current 

capacity. In particular, high conductivity that is closely related to electric flow and the input 

current capacity are the main factors involved in TRC generation. 

To control the active substance generated by ECS, TRC measurement is essential. However, 

ballast water disinfection by ECS finishes within a few seconds, and is therefore technically 

difficult to measure active substance quickly. In particular, the TRC measuring instrument 

requires some warming-up time, so it is difficult to use it in direct connection to the ECS control 

system. However, maximum TRC concentration generated by ECS can be controlled precisely. 
MEPC 57/2/1 

ANNEX 

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I:\MEPC\57\2-1.doc 

3.1.4.2 Composition of TRC control system 

The ECS disinfection system for processing ballast water controls the current wave that is 

closely related to TRC generation and measures electric current and TRC concentration after 

system activation. The system control procedure is as follows: 

.1 The system control first measures the salinity of the ballast water with the fast 

response sensor. 

.2 The measured salinity value is referred to the current density of the rectifier 

through the central control system. The optimum current density is determined on 

the basis of salinity, flow and control of the disinfection level. 

.3 In the same time the TRC value is measured during the ECS process. 

.4 Revise the salinity-current capacity relational equation from the measurements of 

salinity, TRC, and disinfection performance. 

3.1.4.3 Derivation of relational equation for ECS control 

This system is managed on the basis of salinity at which response time is fast and automatic 

measurement is possible. The salinity-electric current relational equation is used to obtain the 

current capacity and the concentration of the active substance, TRC that meets the disinfection 

conditions according to changes water quality. 

3.1.4.4 TRC concentration measurement 

When the ballast water is processed, the TRC concentration can be automatically measured in 

real time by the CLX (HF SCIENTIFIC INC.) system, which is then sent to the main control 

PC for real time monitoring by the online feature. Accordingly, you can adjust the current 

capacity of the electrode in the main control PC to appropriately control the TRC concentration 

during operation. 

3.1.5 Control system PC 

The control system PC controls the operation of ECS and records, reports, and prints all ballast 

operating data, as well as provide alarms. The PC is operated with Windows based program 

allowing user-friendly operation. When the ballast pump runs or stops, the controller detects 

and the control PC supplies or stops the voltage and current of the rectifier, and operates 

the ECS. 

3.1.6 Ballast tanks and discharge 

The active substances react in the pipeline and ballast tanks with both organic and inorganic 

species for effective disinfection. As the active substances reacted with organic and inorganic 

species, micro-organisms are disinfected and TRC concentration inside of ballast tanks are 

reduced. The results of the TRC degradation test within the ballast tank shows (Table 3-1) the 

TRC concentration of 8~10 mg/L to decrease to less than 2 mg/L after 5 days of storage. 
MEPC 57/2/1 

ANNEX 

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Table 3-1. TRC degradation of ECS treated water after 5 days storage in ballast tank 

Site ECS operation TRC concentration after 

5 days (mg/L) 

Ma-san port 1 9.83 1.30 

Ma-san port 2 9.81 1.77 

Ma-san port 3 10.1 1.43 

Ma-san port 4 9.90 0.97 

Ma-san port 5 9.95 1.17 

Sum-jin river 1 9.89 1.63 

Sum-jin river 2 9.74 1.40 

Bu-san port 1 8.31 1.32 

Bu-san port 2 8.65 1.31 

Bu-san port 3 8.77 1.59 

3.2 Summary of system component 

3.2.1 Distributor unit 

Supplies power to ECS components via the power distributor and monitors the state of power 

supply in real time via multifunctional relay (HIMAP). 

3.2.2 Control unit 

z Main Features 

• The Control PC collects and controls all data through the RTU and other 

components by communications. 

• The RTU receives input from the sensors of each component and transfers 

the data to the Control PC. 

3.2.3 Rectifier unit 

z Main Features 

• Rectifier supplies direct current power to electrolysis unit for disinfection. 

• Cooler releases the heat from rectifier to stabilize its performance. 

3.2.4 Electrolyzer 

z Electrolysis unit consists of multiple electrodes and electrolysis module chamber. 

Electrode module is inserted into module chamber. 

z Main features 

• Eliminates micro-organisms, bacteria, etc. from ballast water. 

 • Disinfection of ballast water by electrolysis. 

 • Maintains constant level of disinfection by analyzing conductivity, 

salinity, electric current, etc. in real time. 
MEPC 57/2/1 

ANNEX 

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4 Removal efficacy of micro-organisms 

4.1 Testing body and quality system 

South Sea Institute of KORDI is the testing organization that is accredited by KOLAS 

(The Korea Laboratory Accreditation Scheme) for ISO/IEC 17025 in field of aquatic organisms 

and all disinfection efficacy tests are conducted by the quality system of ISO/IEC 17025. 

KOLAS is the governmental accreditation body in the Republic of Korea. KOLAS evaluates the 

technical competence of testing and calibration laboratories based on the general requirements 

of ISO/IEC 17025, general requirements for the competence of testing and calibration 

laboratories and specific technical requirements of each field. 

The efficacy of ballast water management systems, which make use of active substances 

possible, was evaluated by administration in accordance with guidelines for approval of ballast 

water management systems (G8). The guidelines (G8) include general requirements concerning 

design and construction, technical procedures for evaluation and the procedure for issuance of 

the Type Approval Certificate of ballast water management system. The guidelines (G8) are 

unique compared to the requirements for type approval of traditional marine equipment as type 

approval of ballast water treatment systems requires both land-based and shipboard test. 

4.2 Land-based test 

4.2.1 Information of test barge 

Four test ballast tanks were constructed on the barge, and ECS-300A was installed for the 

land-based test and safety, application, ecological efficacy of ECS was proved. Each of four 

test tanks has 200m3 of volume (Table 4-1). All pipes and valves in each test tanks were 

installed and designed based on the regulation, and the four 500m3

/h ballast pumps were 

installed. For sampling, four tanks for treated water, each has 2m3

 in volume, and four 

controlled water tanks with pipelines and valves were installed. 

Table 4-1. Barge for ECS land-based test specification 

Item Specification 

Name/Type ELECTRO-CLEAN/Barge 

Gross Tonnage 203m3

Dimensions Length 34.31m Width 13.40m Depth 2.4m 

Builder Daeun Shipyard 

Launching 

Date 

May 1, 2006 
MEPC 57/2/1 

ANNEX 

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4.2.2 Result of land-based test 

The land-based tests were performed at two different sites with more than 10 ppt difference in 

salinity according to the G-8 guidelines. The locations of the land-based tests were Ma-san port 

(saline concentration of 28~30ppt) at South sea of Korean peninsular for seawater, and down 

stream of Sum-jin river (saline concentration of 18~20ppt) in Southern area of Korean 

peninsular for brackish water. The Korea Ocean Research and Development Institute performed 

all of the tests that took place and were all in line with D-2 regulations. The tests in Ma-san for 

seawater commenced from 15th April to 30th May 2007 and a total of 5 repetitions were 

performed. The tests in Sum-jin river for brackish water commenced from 1st June 

to 25th July 2007 and a total of 2 repetitions were performed. The working standard of 

TRC concentration by ECS was set at a toxicity concentration of 10 mg/L and the electric 

current and voltage was varied in relation to the quality of environments in which the tests took 

place (salinity, temperature, and contents of organic matter, etc). 

The land-based test was performed successfully a total of five times for seawater and twice for 

brackish water. The result for the disinfection efficacy of brackish water was satisfying. 

But due to the seasonal changes of the Korean brackish water, between 10~50μm of 

micro-organisms were insufficient, therefore micro-organisms have been cultured to fill the 

deficit for further testing to proceed. Further testing is in progress. 

4.3 Shipboard test 

4.3.1 Information of the test vessel 

The specification of M/V STX Yokohama used for shipboard test is summarized in Table 4-2. 

Table 4-2. M/V STX Yokohama specifications 

Component Specifications 

Name/Type M/V STX Yokohama/Container ship 

Gross Tonnage 8,306m3

Dimensions Length: 132.94m Width: 20.50m Depth: 10.50m 

Builder HANJIN 

Launching Date May. 30.1998 

4.3.2 Result of shipboard test 

Shipboard tests have been performed with M/V STX Yokohama, based on Guidelines (G8) to 

prove the efficacy of seawater disinfection. All tests were performed by the Korea Ocean 

Research and Development Institute and test results satisfied D-2 regulation. 

Shipboard tests have been performed with M/V STX Yokohama every week at three different 

regions (East China Sea, Yellow Sea, and Kuroshio Current) from 3rd February to 30th July 2007 

(Total of 24 weeks). 
MEPC 57/2/1 

ANNEX 

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The operation conditions of ECS were controlled to generate 10 mg/L of TRC, where the 

conditions of electric current and voltage were regulated according to the condition of water 

quality of test water during in-ballasting at the test ship (salinity, temperature, and organic 

matter contents etc.). 

5 Data-set 

5.1 Identification 

5.1.1 Identification of active substance 

As a result of comparison to drinking water standards, the disinfection by-products, ozone, 

hydrogen peroxide and bromate of the ECS treated water (except TRC) were seen to be very 

low. In the case of OH-

, which has a very short lifetime during ECS operation, and also as the 

ballast water flows quickly through the ECS, there was no notable effect on disinfection in the 

ballast water. The radicals generated by electrolysis decompose easily without sedimentation. 

Electric potential is an instant process that takes place within the ECS module and it is difficult 

to refer it as an Active Substance (Iksman et al., 1994). And similarly to the basic approval the 

TRC is the active substance for ECS. 

The concentration for active substances can be measured in terms of TRC. From biological 

efficacy tests and preliminary tests results from the land-based and shipboard tests, 10 mg/L of 

TRC is high enough to effectively disinfect micro-organisms in seawater containing various 

concentrations of suspended solids and organic substances, satisfying D-2 standard. From 

these results, the initial concentration of TRC has been controlled at 10 mg/L, even 

though 20~30 mg/L TRC was submitted by the basic approval. Therefore the initial TRC level 

has been reduced from 30 mg/L to 10 mg/L. 

It is not easy to definitely identify all of the active substances from electrolysis of water, due to 

the important role of electrical potential on disinfection of living organisms in ballast water. 

But the identification of active substance as a kind of chemical to generate radicals to treat 

living organisms is summarized in Table 5-1. 

Table 5-1. The identification of hypochlorite 

Item Information 

IUPAC name Hypochlorite 

CAS number 14380-61-1 

UN number 3212 

Molar mass 51.452g/mol 

Empirical formula OClStructural formula 

Purity of technical material and 

identification of impurities 

Bleach, hypochlorous acid, sodium salt; soda bleach; 

sodium oxychloride 

5% of sodium hypochlorite and 95% of water 

Stabilizers or necessary 

additives 

For pools using liquid chlorine (sodium hypochlorite) or 

calcium hypochlorite, add stabilizer (cyanuric acid). 
MEPC 57/2/1 

ANNEX 

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5.1.2 Identification of by-products 

Chlorine is an effective disinfectant for reducing pathogen levels in treated water. However, 

there are concerns with chlorination, which are largely related to formation of chlorination 

by-products (CBPs) formed by reactions between chlorine and other substances present in the 

effluent water. TRC includes free residual chlorine of undissociated and dissociated 

hypochlorite when chlorine is dissolved in water, plus combined residual chlorine of 

chloramines formed by reacting with ammonia. “CBPs” refer to chlorinated organic compounds 

(or total organic halogen) formed by the action of chlorine on the total organic carbon fraction 

of treated water. The two largest identified fractions of CBPs mostly formed by chlorination are 

trihalomethanes (THMs) and haloacetic acids (HAAs). 

Table 5-2 and 5-3 show the analytical results of disinfection by-products from electrolysis of 

brackish and seawater by ECS operation for the production of 10 mg/L of TRC. 

The concentration of disinfection by-products can vary compared to the raw water condition, 

half life and sedimentation, and the toxicity of organisms can be seen to be very low. 

Table 5-2. List of disinfection by-products in the brackish water of Sum-jin river after 

ECS treatment 

List of all potential by-products produced in ballast water

Chemical name CAS number 

Control 

water 

(mg/L) 

Treated 

water 

(mg/L) 

Detection 

limit (mg/L) 

Trichloromethane 000067-66-3 N.D. N.D. < 0.0001 

Bromodichloromethane 000075-27-4 N.D. N.D. < 0.0001 

Dibromochloromethane 000124-48-1 N.D. 0.0083 < 0.0001 

Tribromomethane 000075-25-2 N.D. 0.1081 < 0.0001 

Monochloroacetic acid 000079-11-8 N.D. N.D. < 0.0001 

Dichloroacetic acid 000079-43-6 N.D. N.D. < 0.0001 

Trichloroacetic acid 000076-03-9 N.D. N.D. < 0.0001 

Monobromoacetic acid 000079-08-3 N.D. N.D. < 0.0001 

Dibromoacetic acid 000631-64-1 N.D. 0.0136 < 0.0005 

Tribromoacetic acid 000075-96-7 N.D. 0.0042 < 0.0005 

Bromochloroacetic acid 005589-96-8 N.D. N.D. < 0.0001 

Bromodichloroacetic acid 71333-14-7 N.D. N.D. < 0.0005 

Dibromochloroacetic acid 005278-95-5 N.D. N.D. < 0.0005 

Bromate ion 015541-45-4 N.D. N.D. < 0.002 
MEPC 57/2/1 

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Table 5-3. List of disinfection by-products in the seawater of Ma-san port after 

ECS treatment 

List of ALL potential by-products produced in ballast water

Chemical name CAS number 

Control 

water 

(mg/L) 

Treated 

water 

(mg/L) 

Detection 

limit (mg/L) 

Trichloromethane 000067-66-3 N.D. N.D. < 0.0001 

Bromodichloromethane 000075-27-4 N.D. N.D. < 0.0001 

Dibromochloromethane 000124-48-1 N.D. 0.0093 < 0.0001 

Tribromomethane 000075-25-2 N.D. 0.1231 < 0.0001 

Monochloroacetic acid 000079-11-8 N.D. N.D. < 0.0001 

Dichloroacetic acid 000079-43-6 N.D. N.D. < 0.0001 

Trichloroacetic acid 000076-03-9 N.D. N.D. < 0.0001 

Monobromoacetic acid 000079-08-3 N.D. N.D. < 0.0001 

Dibromoacetic acid 000631-64-1 N.D. 0.0162 < 0.0005 

Tribromoacetic acid 000075-96-7 N.D. 0.0051 < 0.0005 

Bromochloroacetic acid 005589-96-8 N.D. N.D. < 0.0001 

Bromodichloroacetic acid 71333-14-7 N.D. N.D. < 0.0005 

Dibromochloroacetic acid 005278-95-5 N.D. N.D. < 0.0005 

Bromate ion 015541-45-4 N.D. N.D. < 0.002 

Analysis of disinfection by-products was performed. The control and treated samples with 

ECS were collected in Ma-san port (28~30ppt) and Sum-jin river (18~20ppt). The results for 

the various DBP concentrations are listed in Table 5-2 and 5-3. As a result of by-products 

analysis, four kind of by-product have been detected at all test sites, and it was shown that high 

concentration of by-product generated at the Ma-san port than Sum-jin river. 

Table 5-2 and 5-3 show the only four by-products, dibromochloromethane, tribromomethane, 

dibromoacetic acid and tribromoacetic acid that is produced by ECS. The informations of these 

by-products are shown in table-5-4, 5-5, 5-6, 5-7. 

Table 5-4. The information of dibromochloromethane 

Item Information 

IUPAC name Dibromo-chloromethane 

CAS number 124-48-1 

UN number N.A. 

Molar mass 208.28 

Empirical formula ClCHBr2 

Structural formula 

Purity of technical material and identification of impurities 99% of 

dibromochloromethane 

Stabilizers or necessary additives N.A. 
MEPC 57/2/1 

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Table 5-5. The information of tribromomethane 

Item Information 

IUPAC name Bromoform 

CAS number 75-25-2 

UN number 2515 

Molar mass 252.73g/mol 

Empirical formula CHB3 

Structural formula 

Purity of technical material and identification of impurities 100% of bromoform 

Stabilizers or necessary additives Bromoform is relatively 

stable in the air

Table 5-6. The information of dibromoacetic acid 

Item Information 

IUPAC name Dibromoethanoic acid 

CAS number 631-64-1 

UN number N.A. 

Molar mass 217.84 

Empirical formula C2H2Br2O2 

Structural formula 

Purity of technical material and 

identification of impurities 

99% of dibromoacetic acid 

Stabilizers or necessary additives Stable at room temperature in closed 

containers under normal storage and handling 

conditions without stabilizer. 

Table 5-7. The information of tribromoacetic acid 

Item Information 

IUPAC name N.A. 

CAS number 75-96-7 

UN number N.A. 

Molar mass 296.74g/mol 

Empirical formula CBr3COOH

Structural formula 

Purity of technical material and 

identification of impurities 

99% of tribromoacetic acid 

Stabilizers or necessary additives Stable at room temperature in closed 

containers under normal storage and handling 

conditions without stabilizer. 
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5.2 Data-set of hypochlorite 

5.2.1 Aquatic toxicity data 

5.2.1.1 Acute aquatic toxicity data 

Table 5-8. Acute aquatic toxicity of hypochlorite on aquatic organisms 

 Species LC50 

(mg/L/duration) Reference

Fish Pimephales promelas 5.9 (96hr) Curis, et al., 1981 

Crustacea Gammarus fasciatus 4.0 (96hr) Ewell et al., 1986 

Algae Chlorella sorokiniana 0.6 (20hr) Kott et al., 1969 

5.2.1.2 Chronic aquatic toxicity data 

Table 5-9. Chronic aquatic toxicity of hypochlorite on aquatic organisms 

Species LC50 or NOEC 

(mg/L/duration) Reference

Fish Menidia beryl1ina NOEC: 0.18 (7d) Fisher et al., 1994 

Crustacea Dreissena polymorpha LC50: 1.0 (295hr) Martin, I.D. et al., 1993 

Algae Skeletonema costatum EC50: 0.095 (24hr) Gentile J.H. et al., 1976 

5.2.1.3 Information on production of endocrine disruption 

No report on production of endocrine disruption of hypochlorite is available because there’s no 

remaining hypochlorite in living organisms. 

5.2.1.4 Sediment toxicity 

The Log Pow value of sodium hypochlorite is –3.42 (EPI SuitTM, U.S.EPA v3.20) and the Koc 

value of sodium hypochlorite is 14.3 (EPI SuitTM, U.S.EPA v3.20), and it de-hydrolyzes easily 

so the possibility of sediment toxicity would be predicted to be very low. 

5.2.1.5 Bioavailability/Bioconcentration/Biomagnification 

Because of very low Log Pow value of sodium hypochlorite with –3.42 (EPI SuitTM, 

U.S.EPA v3.20), the possibility of predicted Bioavailability/Bioconcentration/Biomagnification 

should be insignificant. 

5.2.1.6 Food web/Population effects 

The Log Pow value of sodium hypochlorite is –3.42 (EPI SuitTM, U.S.EPA v3.20), and so the 

sedimentation of organism is very low. Because of very low Log Pow value of sodium 

hypochlorite, the adverse effect on food web should be insignificant. 
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5.2.2 Mammalian toxicity 

5.2.2.1 Acute mammalian toxicity 

Table 5-10. Acute Toxicity of hypochlorite on mammals 

 Value Species Reference

Oral LD50 (mg/L) 8200 Rat Kaestner, W., cited in BIBRA 

Toxicity Profile 

Dermal LD50 (mg/L) >10000 Rabbit 

Inhalation LC50 (mg/L/4h) >10.5 Rat Bio-fax data summary 

5.2.2.2 Corrosion/Irritation 

Table 5-11. The eye and skin irritation by hypochlorite 

 Species Method Results (including scores 

where available) Reference

Skin Rabbit OECD 404 Irritating, 2%: 1.2, 20%: 5.3, 

35%: 5.2, 50%: 5.3 Loden, M. et al., 1985 

Eye Rabbit Other Irritating, Draize score: 

11 (0.01mL), 40 (0.1mL) Chan, K. Y., 1985 

5.2.2.3 Sensitization 

Table 5-12. The sensitization test of hypochlorite 

 Species Method Results 

(Sensitizer Y/N) Reference

Skin Human Patch test Y Osmundsen, P.E., 1978 

Inhalation N.A. N.A. N.A. N.A. 

5.2.2.4 Repeated-dose toxicity 

Table 5-13. The repeated-dose toxicity test of hypochlorite 

Exposure Route Drinking water 

Exposure Duration 12 months 

Exposure dose 1, 10 or 100 mg/L 

Species Rat 

Method - 

Results Decrease of blood glutathione with 10 or 100 mg/L, increase of 

osmotic fragility after 6 months. In animals exposed for 3 months, the 

3H-thymidine incorporation into nuclei of rat kidney and testes in the 

100 mg/L group was increased. 

Reference Abdel-Rahman, M.S. et al., 1984 
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5.2.2.5 Development and reproductive toxicity 

Table 5-14. The development and reproductive toxicity test of hypochlorite 

Exposure Route Drinking water 

Exposure Duration 6 months 

Exposure dose 10 mg/L residual chlorine 

Species Mouse 

Method Fertility test 

Results No detrimental effects on reproduction. 

NOAEL N.A. 

NOEL N.A. 

Reference Les, E. P., 1968 

5.2.2.6 Carcinogenicity/Mutagenicity 

Table 5-15. The carcinogenicity/mutagenicity test of hypochlorite 

 Species Method Results Reference

Carcinogenicity Mouse Dermal No skin tumors, 

no leukemia. 

Hayatsu, H. et al., 1971 

Mutagenicity Mouse Gavage Negative Meier, J.R. et al., 1985 

5.2.3 Environmental fate and effect under aerobic and anaerobic conditions 

5.2.3.1 Modes of degradation (biotic and abiotic) 

5.2.3.1.1 Decomposition 

The product decomposes slowly on standing with the evolution of oxygen. Factors that increase 

the rate of decomposition are: high initial concentration, increase in temperature, certain 

metallic impurities fall in pH below 11 and exposure to light. 

5.2.3.1.2 Photodegradation 

Half life of 10~15% available chlorine solution will be reduced 3~4 times by sunlight. Half life 

of more than 20% available chlorine solution will be reduced by about 6 times by sunlight. 

5.2.3.2 Partition coefficients 

Table 5-16. The Log Pow and Koc of hypochlorite 

Method Results Reference

Log Pow EPI Suit estimated Essentially zero 

-3.42 

MSDS 

EPI Suite v3.20 

Koc EPI Suit estimated 14.3 EPI Suite v3.20 
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5.2.3.3 Persistence and identification of main metabolites 

Because of low Log Pow and no bioavailability, there was no report on persistence and 

identification of main metabolites in hypochlorite.

5.2.3.4 Reaction with organic matter 

When natural organic matter is treated with hypochlorite species (HOCl, OCl), high molecular 

weight chlorinated compounds form in a first step that is followed by the cleavage of benzene 

rings into trihalomethanes and haloacetic acids. Sodium hypochlorite treated humic acid yielded 

more chloroform than treated fulvic acid. 

5.2.3.5 Potential physical affects on wildlife and benthic habitats 

Sodium hypochlorite is miscible to water (IUCLID, 2000) so it doesn’t affect physical wildlife 

and benthic habitats. 

5.2.3.6 Potential residues in seafoods 

No report on potential residues in seafood of hypochlorite is available. However, sodium 

hypochlorite has low possibility of sediment, and the potential residues in seafood are 

predicted as low. 

5.2.4 Physical and chemical properties 

Table 5-17. Physical and chemical properties of hypochlorite 

Property Value Reference

Melting point (°C) -25°C IUCLID 

Boiling point (°C) 96-99°C IUCLID 

Flammability Non flammable IUCLID 

Density (20 °C; kg/m3) 1.21~1.23g/cm3 IUCLID 

Vapour pressure (20 °C; Pa) 25hPa IUCLID 

Vapour density (air = 1) N.A. MSDS 

Water solubility (temp; effect of 

pH; mg/L) 

Miscible (>11 and 20 degree C) IUCLID 

pH in solution 14 MSDS 

Dissociation constant (pKa) N.A. - 

Oxidation-reduction potential N.A. - 

Corrosivity to material or 

equipment 

N.A. - 

Reactivity to container material N.A. - 

Auto-ignition temperature (°C) N.A. - 

Explosive properties N.A. - 

Oxidizing properties One of the more commonly used 

oxidizing agent and a very efficient 

disinfectant: virucide, bactericidal and 

fungicide. It is used for the remnant 

disinfection of drinkable water 

IUCLID 
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Surface tension N.A. - 

Viscosity Dynamic viscosity 20°C: 2.6mPas IUCLID 

Thermal stability and identity of 

breakdown products 

N.A. - 

Other physical or chemical 

properties 

N.A. - 

5.2.5 Other information 

5.2.5.1 Analytical methods for measuring the concentration at environmentally relevant 

concentrations 

Table 5-18. Analytical methods 

Method DPD method 

Applicability Yes 

Sensitivity Two Ranges: LR – 0.02 to 2.00 mg/L and HR – 0.1 to 8.0 mg/L as Cl2 

Reference Standard Methods for the Examination of Water and Waste Water, 

18th edition, American Public Health Association (APHA), 

5.2.5.2 Risk characterization 

Table 5-20. Acute aquatic toxicity of dibromochloromethane 

 Species LC50 (mg/l/duration) Reference

Fish Cyprinus carpio 52 mg/L (0.75hr/) Trns.Am.Fish.Soc. 

Algae Tetrahymena pyriformis 65 mg/L (24hr) Sci.Total Environ. 

5.3 Data-set of dibromochloromethane 

5.3.1 Toxicity of dibromochloromethane on aquatic organisms 

5.3.1.1 Acute aquatic toxicity data 

Table 5-20. Acute aquatic toxicity of dibromochloromethane 

 Species LC50 (mg/l/duration) Reference

Fish Cyprinus carpio 52 mg/L (0.75hr) Trns.Am.Fish.Soc. 

Algae Tetrahymena pyriformis 65 mg/L (24hr) Sci.Total Environ. 

5.3.1.2 Chronic aquatic toxicity data 

Table 5-21. Chronic aquatic toxicity of dibromochloromethane

Species LC50 or NOEC (mg/l/duration) Reference

Fish Cyprinus carpio LC50: 34 mg/L (NR d) Trns.Am.Fish.Soc. 
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5.3.1.3 Information on endocrine disruption 

Several studies have examined the potential of dibromochloromethane to induce histological 

alterations in endocrine glands following longer-term exposure. No alterations in endocrine 

glands were observed following intermediate-duration exposure of rats to 200 or 256 mg/kg/day 

(Chu et al. 1982b; Daniel et al. 1990) or rats or mice to 250 mg/kg for 5 days/week (NTP 1985). 

Administration of dibromochloromethane via gavage for 2 years resulted in thyroid follicular 

cell hyperplasia in mice exposed to 50 or 100 mg/kg (5 days/week). No effects were observed 

in rats administered 40 or 80 mg/kg (5 days/week) (NTP 1985). No effects on serum 

testosterone levels were observed in rats given gavage doses of 160 mg/kg/day for 7 days. 

However, a decrease in levels resulted from doses of 310 mg/kg/day (Potter et al. 1996). 

5.3.1.4 Sediment toxicity 

Both tribromomethane and dibromochloromethane are relatively stable in the air, but reactions 

with other chemicals in the air cause them to break down slowly (about 50% in 1 or 2 months). 

Dibromochloromethane in water or soil may also be broken down by bacteria, but the speed of 

this process is not known. Log Pow value of dibromochloromethane is 2.16 and it is 

relatively low. 

5.3.1.5 Bioavailability/Biomagnification/Bioconcentration 

The bioaccumulative potential of an organic chemical reflects the tendency of a chemical to be 

taken up and retained by an aquatic organism, both from water and through food, which then 

results in higher concentration of that chemical in an organism than in its environment. Log Pow 

is a common term to classify chemicals as bioaccumulative. And Log Pow value of 

dibromochloromathane is 2.24. 

5.3.1.6 Food web/Population effects 

The Log Pow value of dibromochloromethane is 2.16 (CITI 1992; Sangster 1994), and so the 

sedimentation of organism is very low. Therefore, possibility of sedimentation in food web as 

the level goes up is predicted very low. Dibromochloromethane does not build up in the 

food chain. 

5.3.2 Mammalian toxicity 

5.3.2.1 Acute mammalian toxicity 

Table 5-22. Acute Toxicity of dibromochloromethane 

 Value Species Reference

Oral LD50 (mg/l) 848-1186 (mg/kg) Rat Chu I et al., 1980 
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5.3.2.2 Corrosion/Irritation 

Table 5-23. The eye and skin irritation by dibromochloromethane 

 Species Method Results (including scores 

where available) Reference

Skin Rats and 

mice 

Gavage for up 

to 2 years 

No histological alterations 

were found in the skin of rats 

and mice 

NTP1985,1989a 

Eye Rats and 

mice 

Gavage for up 

to 2 years 

No histological alternations 

were found in the skin of rats 

and mice 

NTP 1985,1989a 

5.3.2.3 Sensitization 

No skin and inhalation sensitization is given to dibromochloromethane. This is, however, 

primarily due to lack of information, and skin contact with dibromochloromethane should 

be minimized. 

5.3.2.4 Repeated-dose toxicity 

Table 5-24. The repeated-dose toxicity test of dibromochloromethane 

Exposure Route Eating 

Exposure Duration 90 days 

Exposure dose 0,50,100,and 200 mg 

Species Rat 

Method - 

Results No changes were found in mortality, clinical signs, 

ophthalmoscopic examinations, or hematology that was considered 

to be related to treatment. Mean final body weight and body weight 

gain were significantly decreased in male and female high dose 

animals relative to the vehicle control. 

Reference Daniel FB, 1990 

5.3.2.5 Development and reproductive toxicity 

Table 5-25. The development and reproductive toxicity test of dibromochloromethane 

Exposure Route GO (gavage oil) 

Exposure Duration 9 days 

Exposure dose 200 mg/kg/day 

Species Rat 

Method - 

Results No alternation in the number of resorption sites, fetuses per litter, 

fetal body weights fetal gross malformations, or skeletal or visceral 

anomalies were found. 

NOAEL 200 mg/kg/day 

NOEL N.A. 

Reference Ruddick et al. (1983) 
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5.3.2.6 Carcinogenicity/Mutagenicity 

Table 5-26. The carcinogenicity/mutagenicity test of dibromochloromethane 

 Species Method 

Details Results Reference

Carcinogenicity Mice 

gavage doses 

of 100 mg/kg, 

5 days/week 

for 2 years 

Increases in the incidences 

of hepatocellular 

adenomas and carcinomas NTP 1985 

Mutagenicity 

Rat and 

mouse 

- Positive Melnick et al

1998 

5.3.3 Environmental fate and effect under aerobic and anaerobic conditions 

5.3.3.1 Modes of degradation (biotic and abiotic) 

Table 5-27. The modes of degradation of dibromochloromethane 

Seawater 

or Fresh 

water 

Test 

duration Results Break-down products Reference 

Hydrolysis Chlorinated 

water 28 days 

The concentration 

of 

dibromochloromet

hane decreased 

from 46μg/L to 

3μg/L 

- Nicholson 

et al. 2002 

Biodegradation 

under 

aerobic 

conditions 

N.A. N.A. 

Increased 

degradation rates 

were observed 

N.A. 

Kenneke et 

al. 2003 

Pecher et 

al. 2002 

5.3.3.2 Partition coefficients 

Table 5-28. The Log Pow and Koc of dibromochloromethane 

 Method Results Reference

Log Pow EPI Suit estimated 2.16 at 25°C CITI 1992; Sangster 1994 

Koc EPI Suit estimated 35.04 EPI Suit V 3.20 

5.3.3.3 Persistence and identification of main metabolites 

Because of low Log Pow and no bioavailability, there was no report on persistence and 

identification of main metabolites in dibromochloromethane. 
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5.3.3.4 Reaction with organic matter 

No report on reaction with organic matter of dibromochloromethane is available.

5.3.3.5 Potential physical affects on wildlife and benthic habitats 

Density of dibromochloromethane (2450kg/m3 at 20°C) is higher than density of 

seawater (1025kg/m3

), and dibromochloromethane is slightly soluble with 2.7 x 10 mg/L of 

water solubility at 20°C. Therefore, it may have potential physical effects on wildlife and 

benthic habits. 

5.3.3.6 Potential residues in seafood 

No report on potential residues in seafood of dibromochloromethane is available. However, 

dibromochloromethane has low possibility of sediment, and the potential residues in seafood are 

predicted as low. 

5.3.4 Physical and chemical properties 

Table 5-29. Physical and chemical properties of dibromochloromethane 

Property Value Reference

Melting point (°C) -20°C Lide 2000 

Boiling point (°C) 120°C Lide 2000 

Flammability (flash point for 

liquids; °C) Non-flammable HSDB2004a,2004b 

Density (20 °C; kg/m3) 2.451g/cm3

 Lide 2000 

Vapour pressure (20 °C; Pa) 76 mmgHg US EPA Mabey et al. 1982 

Vapour density (air = 1) No data IARC 1991a, 1991b 

Water solubility (temp; effect of 

pH; mg/l) 2.7x103

mg/L (20°C) Horvath 1982; Heikes 1987 

5.3.5 Other information 

5.3.5.1 Analytical methods for measuring the concentration at environmentally relevant 

concentrations 

Table 5-30. Analytical methods 

Method GC/HSD (gas chromatography – halide specific detector) 

Applicability Contaminated soil 

Sensitivity Sample detection limit: 0.9 μg/kg/Accuracy (percent recovery) : 94 

Reference EPA 1986a 
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5.3.5.2 Risk characterization 

Table 5-31. Some indices for risk characterization of dibromochloromethane 

Persistent Bioaccumulative Toxic Reference

No 

Half life (flowing aerated 

water): 0.7-398 hr 

No 

BCF: 9.188 

- Kaczmar et al. 1984 

Mackay et al. 1982 

5.4 Tribromomethane 

5.4.1 Toxicity of tribromomethane on aquatic organisms 

5.4.1.1 Acute aquatic toxicity data 

Table 5-32. Acute aquatic toxicity of tribromomethane on aquatic organisms 

Species LC50 

(mg/l/duration) Reference

Fish Brevoortia 

tyrannus 12 mg/L (96hr) Quarterly Progress Report, 1978. 

Crustacea Penaeus aztecus 26 mg/L (96hr) Quarterly Progress Report, 1978. 

Algae Selenastrum 

capricornutum 

40 mg/L (96hr) 

(EC50) 

Contract No.68-01-4646,U.S. 

EPA 

5.4.1.2 Chronic aquatic toxicity data 

Table 5-33. Chronic aquatic toxicity of tribromomethane on aquatic organisms 

Species LC50 or NOEC 

(mg/l/duration)

Reference

Fish Cyprinodon 

variegatus 

NOEC 2.9 mg/L 

(96hr) 

Bull.Environ.Contam. Toxicol. 

27(5):596-604 (OECDG Data 

File) 

Crustacea Penaeus 

aztecus 0.030 mg/L 

Pacific.NorthwestLab., 

Richland.WA:40p (U.S.NTIS 

NUREG. 

CR-1297) 

Algae Selenastrum 

capicornutum 

NOEC 10 mg/L 

(96hr) 

Contract No.68-01-4646, 

U.S.EPA: 9p 

5.4.1.3 Information on endocrine disruption 

Several endocrine effects have been observed in animals exposed to tribromomethane; however, 

none of the effects were consistently found. The observed endocrine effects included enlarged 

thyroid gland in rats administered a lethal dose of 800 mg/kg/day for 14 days (NTP 1989a), 

decreased thyroid follicular size and colloid density 90 days after termination of exposure 

to 360 mg/kg/day (Chu et al. 1982b), thyroid follicular cell hyperplasia in mice 

administered 200 mg/kg (5 days/week) for 2 years (NTP 1989a), pituitary gland hyperplasia in 

rats administered 100 mg/kg (5 days/week), but not 200 mg/kg (NTP 1989a), and decreased 

serum testosterone levels in rats exposed to 380 mg/kg/day for 7 days (Potter et al. 1996). 
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5.4.1.4 Sediment toxicity 

Generally, tribromomethane is relatively stable in the air, but reactions with other chemicals in 

the air cause them to break down slowly (about 50% in 1 or 2 months). Tribromomethane in 

water or soil may also be broken down by bacteria, but the speed of this process is not known. 

According to CITI (1992) and Sangster (1994), the value of Log Pow is 2.4, which is smaller 

than the indicated value of bioaccumulation which is 3. And Koc value from EPI Suit V 3.20 

is 35.04 and it is smaller than 500l/kg. Therefore, it is considered to have low possibility of 

sediment toxicity. 

5.4.1.5 Bioavailability/Biomagnification/Bioconcentration 

The value of Log Pow is 2.4 and the value smaller than low Pow is 3 which is the rough 

indication for bioaccumulation and the value BCF with using method of regression-based 

was 14.06 which is smaller than the value of BCF>2000. It is considered to be not high value to 

bioaccumulation. 

5.4.1.6 Food web/Population effects 

The value of Log Pow is 2.4 and the value smaller than low Pow is 3 which is the rough 

indication for bioaccumulation and the value BCF with using method of regression-based 

was 14.06 which is smaller than the value of BCF>2000. It is considered to be not high value to 

bioaccumulation, and tribromomethane does not build up in the food chain. 

5.4.2 Mammalian toxicity 

5.4.2.1 Acute mammalian toxicity 

Table 5-34. Acute Toxicity of tribromomethane 

 Value Species Reference

Oral LD50 (mg/kg) 1147 mg/kg Rat Chu et al 1982a 

5.4.2.2 Corrosion/Irritation 

Table 5-35. The eye and skin irritation by tribromomethane 

 Species Method Results Reference

Skin Rats and mice - No affect NTP 1985, 1989a

Eye Rats and mice - No affect NTP 1985, 1989a

5.4.2.3 Sensitization 

No skin and inhalation sensitization is given to tribromomethane. This is, however, primarily 

due to lack of information, and skin contact with liquid tribromomethane should be minimized. 
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5.4.2.4 Repeated-dose toxicity

Table 5-36. The repeated-dose toxicity test of tribromomethane 

Exposure Route Receiving gavage 

Exposure Duration 2 years 

Exposure dose 200 mg/kg/(5day/week) 

Species Rats and mice 

Method - 

Results No significant histopathological alterations were detected 

NOAEL N.A. 

NOEL N.A. 

Reference NTP(1989a) 

5.4.2.5 Development and reproductive toxicity 

Table 5-37. The development and reproductive toxicity test of tribromomethane 

Exposure Route GO (gavage oil) 

Exposure Duration 9 days 

Exposure dose 200 mg/kg/day 

Species Rat 

Method - 

Results Increase in the occurrence of skeletal anomalies in offspring of rats 

NOAEL 100 mg/kg/day 

Reference Ruddick et al. (1983) 

5.4.2.6 Carcinogenicity/Mutagenicity 

The available data are too limited to fully evaluate the contribution of these pathways to the 

genotoxicity and carcinogenicity of tribromomethane. 

Table 5-38. The carcinogenicity/mutagenicity test of tribromomethane 

 Species Method Details Results Reference

Carcinogenicity

Rat and 

mouse 

Rats (50/sex/group) and mice 

(50/sex/group) were administered 

tribromomethane in corn oil by 

gavage 5 days/week for 2 years 

at 0, 100, or 200 mg/kg (rats and 

female mice) or 0, 50, or 

100 mg/kg (male mice). 

Sufficient NTP, 1988 

Mutagenicity 

Rat and 

mouse 

- Positive Melnick et 

al 1998 
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5.4.3 Environmental fate and effect under aerobic and anaerobic conditions 

5.4.3.1 Modes of degradation (biotic and abiotic) 

Table 5-39. The modes of degradation of tribromomethane 

Water Test 

duration Results Break-down products Reference 

Hydrolysis 

Chlorinated 

water 

7 days 

Decreased 

from 58μg/L 

to <1μg/L 

N.A. 

Nicholson et al. 

2002 

Biodegradation N.A. N.A. Increase in 

degradation Dibromomethane 

Kenneke et al. 

2003; Pecher et 

al. 2002 

Half life Fresh 

water N.A. 5.836hr. N.A. EPI Suit V 3.20

5.4.3.2 Partition coefficients

Table 5-40. The Log Pow and Koc of tribromomethane 

Method Results Reference

Log Pow Other (Measured) 2.4 at 25°C CITI1992; Sangster 1994 

Koc (Log Koc) N.A. 35.04 (1.545) EPI Suit V 3.20 

5.4.3.3 Persistence and identification of main metabolites 

Because of low Log Pow and no bioavailability, there was no report on persistence and 

identification of main metabolites in tribromomethane. 

5.4.3.4 Reaction with organic matter 

No report on reaction with organic matter of tribromomethane is available. 

5.4.3.5 Potential physical affects on wildlife and benthic habitats 

Density of tribromomethane (2890kg/m3

 at 20°C) is higher than density of seawater (1025kg/m3), 

and tribromomethane is slightly soluble with 3.1 x 10 mg/L of water solubility at 25°C. Therefore, 

it may have potential physical effects on wildlife and benthic habits. 

5.4.3.6 Potential residues in seafood 

No report on potential residues in seafood of tribromomethane is available. However, 

tribromomethane has low possibility of sedimentation, and the potential residues in seafood are 

predicted as low. 
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5.4.4 Physical and chemical properties 

Table 5-41. Physical and chemical properties of tribromomethane 

Property Value Reference

Melting point (°C) -11.87°C EPI Suit V 3.20 

Boiling point (°C) 167.23°C EPI Suit V 3.20 

Flammability Non-flammable HSDB 2004a ,2004b 

Density (20 °C; kg/m3) 2.899g/cm3 Lide, 2000 

Vapour pressure (25 °C; mmHg) 5.34mmHg EPI Suit V 3.20 

Vapour density (air = 1) 8.7 IARC 1991a, 1991b 

Water solubility 3.10x103

mg/L (25°C) 

Slightly soluble EPI Suit V 3.20 

Surface tension 41.53dynes/cm Lewis 1997 

Viscosity at 20°C : 0.58mPas MSDS 

5.4.5 Other information 

5.4.5.1 Analytical methods for measuring the concentration at environmentally relevant 

concentrations 

Table 5-42. Analytical methods 

Method GC-HSD (gas chromatography – halide specific detector) 

Applicability Contaminated soil 

Sensitivity Sample detection limit : 2μg/kg/Accuracy (percent recovery) : 96 

Reference EPA 1986a 

5.4.5.2 Risk characterization 

Table 5-43. Some indices for risk characterization of tribromomethane 

Persistent Bioaccumulative Toxic Reference

No 

Half life (flowing aerated 

water): 1-581 hr 

No 

BCF: 14.06 

No 

NOEC: 2.9-

10 mg/L 

Kaczmar et al. 1984 

Mackay et al. 1982 

5.5 Dibromoacetic acid 

5.5.1 Toxicity of dibromoacetic acid on aquatic organisms 

5.5.1.1 Acute aquatic toxicity data 

No report on production of acute aquatic toxicity data of dibromoacetic acid is available. 

5.5.1.2 Chronic aquatic toxicity data 

No report on production of chronic aquatic toxicity data of dibromoacetic acid is available. 
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5.5.1.3 Information on endocrine disruption 

No report on production of endocrine disruption of dibromoacetic acid is available. 

5.5.1.4 Sediment toxicity 

The Log Pow value of dibromoacetic acid is 0.7 (EPI SuitTM, U.S.EPA v3.20) and the Koc value 

of dibromoacetic acid is 1.895 (EPI SuitTM, U.S.EPA v3.20) so the possibility of sediment 

toxicity would be predicted to be very low. 

5.5.1.5 Bioavailability/Biomagnification/Bioconcentration 

Because of very low Log Pow value of dibromoacetic acid with 0.7 (EPI SuitTM, 

U.S.EPA v3.20) and low BCF value of dibromoacetic acid with 3.162(EPI SuitTM, 

U.S.EPA v3.20), the possibility of predicted Bioavailability/Bioconcentration/Biomagnification 

is considered to be low. 

5.5.1.6 Food web/Population effects 

The Log Pow value of dibromoacetic acid is 0.7 (EPI suit), and so the sedimentation of 

organism is very low. Therefore, possibility of sedimentation in food web as the level goes up 

is predicted very low. Dibromoacetic acid does not build up in the food chain. 

5.5.2 Mammalian toxicity 

5.5.2.1 Acute mammalian toxicity 

Table 5-44. Acute Toxicity of dibromoacetic acid on mammals 

Value Species Reference

Oral LD50 (mg/l) 4480 Rat Woodard et al., 1941 

5.5.2.2 Corrosion/Irritation 

Dibromoacetic acid may be harmful by inhalation, in contact with skin and if swallowed and it 

may cause burns. 

5.5.2.3 Sensitization 

No report on production of sensitization of dibromoacetic acid is available. 
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5.5.2.4 Repeated-dose toxicity 

Table 5-45. The repeated-dose toxicity test of dibromoacetic acid 

Exposure Route Gavage 

Exposure 

Duration 14 days 

Exposure dose 0, 5, 50, or 250 mg/kg of body weight per day 

Species Rats 

Method - 

Results No effects on body or testicular weights, epididymal weight in 

the 250 mg/kg group was significantly lower than that of the control 

group 

Reference Tsuchiya T et al., 2000 

5.5.2.5 Development and reproductive toxicity 

Table 5-46. The development and reproductive toxicity test of dibromoacetic acid 

Exposure Route Drinking water 

Exposure 

Duration 14 days 

Exposure dose 0, 50, 250 or 650 mg/L 

Species Sprague-Dawley rats (2-generations) 

Method N.A. 

Results Reproductive effects were seen in high-dose F1 males: a significant 

increase in the unilateral malformation of the reproductive tract 

(small or absent epididymides, and small, testis) was seen. 

NOAEL 50 mg/L 

Reference Christian et al., 2002 

5.5.2.6 Carcinogenicity/Mutagenicity 

Table 5-47. The carcinogenicity/mutagenicity test of dibromoacetic acid 

 Species Method Details Results Reference

Carcinogenicity 

Rats and 

mice 

Exposure to 

dibromoacetic acid 

in drinking water for 

2 weeks, 3 months, 

or 2 years. 

Concentrations were 

0, 125, 250, 500, 

1000, and 2000 mg/L 

Toxic effects of 

dibromoacetic acid 

in the prechronic 

studies were 

detected in the 

liver and testes. 

Ronald L et al., 

2007 

Mutagenicity 

Male 

mice 

Orally via drinking 

water for 13 weeks 

Detailed results of 

the study are not 

available at this 

time. 

NTP, 2003c 
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5.5.3 Environmental fate and effect under aerobic and anaerobic conditions 

5.5.3.1 Modes of degradation (biotic and abiotic) 

Table 5-48. The Modes of degradation of dibromoacetic acid 

Water Test 

duration Results 

Breakdown 

products 

Reference 

Biodegradation Drinking 

water 6 months 

Biodegradation 

was observed for 

each of the 

HAAs 

Chloride Bethany M,2004 

5.5.3.2 Partition coefficients

Table 5-49. The Log Pow and Koc of dibromoacetic acid 

 Method Results Reference

Log Pow EPI Suit estimated 0.7 EPI SUIT V3.20 

Koc EPI Suit estimated 0.278 EPI SUIT V3.20 

5.5.3.3 Persistence and identification of main metabolites 

Because of low Log Pow and no bioavailability, there was no report on persistence and 

identification of main metabolites in dibromoacetic acid. 

5.5.3.4 Reaction with organic matter 

No report on reaction with organic matter of dibromoacetic acid is available.

5.5.3.5 Potential physical affects on wildlife and benthic habitats 

Density of dibromoacetic acid (2450kg/m3

 at 20°C) is higher than density of 

seawater (1025kg/m3

), and dibromoacetic acid is slightly soluble with 2.214 x 104mg/L of water 

solubility at 20°C. Therefore, it might have potential physical effects on wildlife and 

benthic habits. 

5.5.3.6 Potential residues in seafood 

No report on potential residues in seafood of dibromoacetic acid is available. However, 

dibromoacetic acid has low possibility of sedimentation, and the potential residues in seafood 

are predicted as low. 
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5.5.4 Physical and chemical properties 

Table 5-50. Physical and chemical properties of dibromoacetic acid 

Property Value Reference

Melting point (°C) 49 ̊C Windholz et al., 1996; Lide, 1999 

Boiling point (°C) 195 ̊C Adapted Stein & Brown method 

Flammability N.A. N.A. 

Density (20 °C; g/cm3) N.A. N.A. 

Vapour pressure (25 °C ; Pa) 0,023mmHg N.A. 

Vapour density (air = 1) N.A. N.A. 

Water solubility (temp; effect 

of pH; mg/l) 

2.214 x 104 at 20  ̊C 

(mg/l) Windholz et al., 1996; Lide, 1999 

5.5.5 Other information 

5.5.5.1 Analytical methods for measuring the concentration at environmentally relevant 

concentrations 

Table 5-51. Analytical methods 

Method GC/ECD (Gas chromatography-Electron capture detector) 

Applicability Contaminated water 

Sensitivity Accuracy: 93-116% (US EPA method standard) 

Reference US EPA 552.2 

5.5.5.2 Risk characterization 

Table 5-52. Some indices for risk characterization of dibromoacetic acid 

Persistent Bioaccumulative Toxic Reference

No No 

BCF: 3.162 - EPI Suit V 3.20 

5.6 Tribromoacetic acid 

5.6.1 Toxicity of tribromoacetic acid on aquatic organisms 

5.6.1.1 Acute aquatic toxicity data 

No report on acute aquatic data of tribromoacetic acid is available. 

5.6.1.2 Chronic aquatic toxicity data 

No report on chronic aquatic data of tribromoacetic acid is available. 

5.6.1.3 Information on endocrine disruption 

No report on endocrine disruption of tribromoacetic acid is available. 
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5.6.1.4 Sediment toxicity 

The Log Pow value of tribromoacetic acid is 1.71 (EPI SuitTM, U.S.EPA v3.20) and the Koc 

value of tribromoacetic acid is 0.437 (EPI SuitTM, U.S.EPA v3.20) so the possibility of sediment 

toxicity would be predicted to be very low. 

5.6.1.5 Bioavailability/Biomagnification/Bioconcentration 

Because of very low Log Pow value of tribromoacetic acid with 1.71 (EPI SuitTM, U.S.EPA v3.20) 

and low BCF value of tribromoacetic acid with 3.162(EPI SuitTM, U.S.EPA v3.20), the possibility of 

predicted Bioavailability/Bioconcentration/Biomagnification is considered to be low. 

5.6.1.6 Food web/Population effects 

The Log Pow value of tribromoacetic acid is 1.71 (EPI suit), and so the sedimentation of 

organism is very low. Therefore, possibility of sedimentation in food web as the level goes up 

is predicted very low. Tribromoacetic acid does not build up in the food chain. 

5.6.2 Mammalian toxicity 

5.6.2.1 Acute mammalian toxicity 

No report on acute mammalian toxicity of tribromoacetic acid is available. 

5.6.2.2 Corrosion/Irritation 

Information about the corrosion and irritation is not enough. However, general corrosion and 

irritation information are given from MSDS of tribromoacetic acid. According to MSDS sheet, 

corrosive and irritant effect may be shown on skin and mucous membranes and it is also 

considered to have strong corrosive and irritant effect on the eye. 

5.6.2.3 Sensitization

No sensitizing effects are known. 

5.6.2.4 Repeated-dose toxicity 

Table 5-53. The repeated-dose toxicity test of tribromoacetic acid 

Exposure Route Drinking water 

Exposure 

Duration 2 weeks 

Exposure dose 0, 30, 100, 300, and 500 mg/L 

Species Rats 

Method - 

Results During the treatment period, all animals survived to the scheduled 

necropsy and there were no clinical signs of general toxicity noted at any 

dose level. There were no treatment-related findings in body weights or 

feed consumption, but there was a slight and inconsistent decrease in 

water consumption in the 400 mg/L animals. 

Reference NTP Study Number: RDGT94009 
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5.6.2.5 Development and reproductive toxicity 

Table 5-54. The development and reproductive toxicity test of tribromoacetic acid 

Exposure Route Drinking water 

Exposure 

Duration 

2 weeks 

Exposure dose 39 mg/kg/day 

Species Rats 

Method N.A. 

Results Female and male reproductive findings were unremarkable. 

Reference NTP Study Number: RDGT94009 

5.6.2.6 Carcinogenicity/Mutagenicity 

Table 5-55. The carcinogenicity/mutagenicity test of tribromoacetic acid 

 Species Method Details Results Reference

Mutagenicity Salmonella - positive Knasmuller,1999 

5.6.3 Environmental fate and effect under aerobic and anaerobic conditions 

5.6.3.1 Modes of degradation (biotic and abiotic) 

Information about the biodegradation of HAAs within water distribution systems is altogether 

lacking. Thus, in situ studies of HAA biodegradation (including those HAAs not studied 

herein) in natural waters and drinking water distribution systems are still needed to confirm our 

hypothesis that bacteria play an important role in the fate of HAAs in these systems. 

Table 5-56. The modes of degradation of tribromoacetic acid 

Seawater 

or Fresh 

water 

Test 

duration 

Results Breakdown 

products 

Reference 

Biodegradation 

under aerobic 

conditions

Drinking 

water 6 months 

Biodegradation 

was observed 

for each of the 

HAAs 

Chloride Bethany 

M, 2004 

5.6.3.2 Partition coefficients

Table 5-57. The Log Pow and Koc of tribromoacetic acid 

 Method Results Reference

Log Pow EPI Suit estimated 1.71 EPI SUIT V3.20 

Koc EPI Suit estimated 2.738 EPI SUIT V3.20 
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5.6.3.3 Persistence and identification of main metabolites 

 

Because of low Log Pow and no bioavailability, there was no report on persistence and 

identification of main metabolites in tribromoacetic acid. 

5.6.3.4 Reaction with organic matter 

No report on reaction with organic matter of tribromoacetic acid is available. 

5.6.3.5 Potential physical affects on wildlife and benthic habitats 

 

Density of tribromoacetic acid (1.980kg/m3

 at 20°C) is higher than density of 

seawater (1025kg/m3

), and tribromoacetic acid is slightly soluble with 1.199 x 104mg/L of water 

solubility at 25°C. Therefore, it might have potential physical affects on wildlife and 

benthic habits. 

5.6.3.6 Potential residues in seafood 

No report on potential residues in seafood of tribromoacetic acid is available. However, 

tribromoacetic acid has low possibility of sediment, and the potential residues in seafood are 

predicted as low. 

5.6.4 Physical and chemical properties 

Table 5-58. Physical and chemical properties of tribromoacetic acid 

Property Value Reference 

Melting point (°C) 130 - 133 ̊C MSDS 

Boiling point (°C) 245°C MSDS 

Flammability N.A. N.A. 

Density (20 °C; kg/m3) - - 

Vapour pressure (20 °C; Pa) 50 mmHg US EPA Mabey et al, 1982 

Vapour density (air = 1) N.A. N.A. 

Water solubility (temp; effect of 

pH; mg/l) 1.199 x 104

 at 25°C US EPA Mabey et al, 1985 

5.6.5 Other information 

5.6.5.1 Analytical methods for measuring the concentration at environmentally relevant 

concentrations

Table 5-59. Analytical methods 

Method GC/ECD (Gas chromatography - Electron capture detector) 

Applicability Contaminated water 

Sensitivity Accuracy: 93~116% (US EPA method standard) 

Reference US EPA 552.2 
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5.6.5.2 Risk characterization 

Table 5-60. Some indices for risk characterization of tribromoacetic acid 

Persistent Bioaccumulative Toxic Reference

No No 

BCF: 3.162 - EPI SUIT V3.20 

6 Toxicity tests with ECS treated water

The toxicity tests of discharging ballast water after ECS operation were done by the Kyung-hee 

University. The laboratory of the Kyung-hee University conducted the tests according to the 

standard procedures for toxicity tests of US EPA International standard procedures. 

The laboratory was established and maintained the procedures for identification, collection, 

indexing, access, storage, maintenance and disposal of quality and technical records as a quality 

assurance document. 

6.1 Test conditions 

The toxicity of the treated ECS water was tested in order to determine its safety to the ecological 

environment. The three different aquatic organisms in different three trophic level, algae, 

invertebrate, and fish were tested. 

Due to the volatile characteristics of the complex radicals in electrolyzed water, the treated 

group was set with 0, 25, 50, 75 and 100% of dilution with culture media or raw water for acute 

(LC 50 – 96hrs) and some chronic toxicity tests according to the results of previous tests in the 

Lab and references. The tests were done with two different sampling times of discharging 

water after ECS operation at two different locations, respectively. The toxicity tests were 

performed 3 days and 5 days after being treated with ECS and in both brackish and seawater. 

All of the samples that were used for the treated ballast water were collected from the barge. 

The ECS treated samples for brackish water were collected from Sum-jin river (18ppt) and 

seawater from Ma-san port (30ppt). The measured TRC after 3 and 5 days was 0.2~1.6 

and 0.2~0.9 mg/L after dilution, respectively. 

6.2 Results of toxicity tests 

6.2.1 Treated brackish water which of short time passed after ECS 

6.2.1.1 Acute toxicity test 

Table 6-1. Acute toxicity test with treated brackish water from 3 days after ECS operation 

Species LC50 (mg/L) Comments, etc.

Invertebrate Artemia nauplii 1.0 (96hr) 50% artificial brackish water + 

50% ECS treated water 

Fish Poecilia latipinna 1.7 (96hr) 25% artificial brackish water + 

75% ECS treated water 
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6.2.1.2 Chronic toxicity test 

Table 6-2. Chronic toxicity test with treated brackish water from 3 days after 

ECS operation 

Species NOEC 

(mg/L) Comments, etc.

Algae Skeletonema costatum 0.8 (96hr) 50% F/2 medium (15ppt) + 50% 

ECS treated water 

Invertebrate Artemia nauplii 0.9 (21d) 60% artificial brackish water + 

40% ECS treated water 

Fish Poecilia latipinna 1.1 (62d) 60% artificial brackish water + 

40% ECS treated water 

6.2.2 Treated seawater which of short time passed after ECS 

6.2.2.1 Acute toxicity test 

Table 6-3. Acute toxicity test with treated seawater from 3 days after ECS operation 

Species LC50 

(mg/L) Comments, etc.

Invertebrate Monocorophium 

acherusicum 1.4 (96hr) 25% artificial seawater + 

75% ESC treated water 

Fish Paralichthys olivaceus 0.9 (96hr) 50% artificial seawater + 

50% ECS treated water 

6.2.1.2 Chronic toxicity test 

Table 6-4. Chronic toxicity test with treated seawater from 3 days after ECS operation 

Species NOEC 

(mg/L) Comments, etc.

Algae Skeletonema costatum 0.6 (96hr) 75% F/2 medium (30ppt) + 25% 

ECS treated water 

Invertebrate Monocorophium 

acherusicum 1.0 (21d) 60% artificial seawater + 

40% ECS treated water 

Fish Paralichthys olivaceus 1.0 (62d) 70% artificial seawater + 

30% ECS treated water 
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6.2.3 Treated brackish water which of long time passed after ECS 

6.2.3.1 Acute toxicity test 

Table 6-5. Acute toxicity test with treated brackish water from 5 days after ECS operation 

Species LC/EC50 

(mg/L) Comments, etc.

Invertebrate Artemia nauplii 1.0 (96hr) 50% artificial brackish water + 

50% ECS treated water 

Fish Poecilia latipinna 1.1 (96hr) 25% artificial brackish water + 

75% ECS treated water 

6.2.3.2 Chronic toxicity test 

Table 6-6. Chronic toxicity test with treated brackish water from 5 days after 

ECS operation 

 Species NOEC 

(mg/L) Comments, etc.

Algae Skeletonema costatum 0.5 (96hr) 50% F/2 medium (15ppt) + 50% 

ECS treated water 

Invertebrate Artemia nauplii 0.5 (21d) 60% artificial brackish water + 

40% ECS treated water 

Fish Poecilia latipinna 1.0 (21d) 60% artificial brackish water + 

40% ECS treated water 

6.2.4 Treated seawater which of long time passed after ECS 

6.2.4.1 Acute toxicity test 

Table 6-7 Acute toxicity test with treated seawater from 5 days after ECS operation 

 Species LC/EC50 

(mg/L) Comments, etc.

Invertebrate Monocorophium 

acherusicum 1.2 (96hr) 100% ECS treated water 

Fish Paralichthys olivaceus 1.1 (96hr) 25% artificial seawater + 

75% ECS treated water 

6.2.4.2 Chronic toxicity test 

Table 6-8. Chronic toxicity test with treated seawater from 5 days after ECS operation 

 Species NOEC 

(mg/L) Comments, etc.

Algae Skeletonema costatum 0.3 (96hr) 75% F/2 medium (30ppt) + 

25% ECS treated water 

Invertebrate Monocorophium 

acherusicum 0.6 (21d) 60% artificial seawater + 40% 

ECS treated water 

Fish Paralichthys olivaceus 0.9 (62d) 60% artificial seawater + 40% 

ECS treated water 
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6.3 Test results 

The result of the toxicity test of discharging water with different storing times after 

ECS operation in seawater and brackish water, show that the discharged water which had been 

stored for three days showed higher toxicity than that of stored for five days. Because of the 

unstable characteristics of oxidants in water, the measured range of TRC in test water showed 

various range even though the dilution volume of treated water was accurate. The result shows 

that the disinfectants for organisms from ECS operation decreased rapidly for couple of days 

and then become less volatile and deficient decomposer with the passage of time. 

Realistic testing in the aquatic system shows a reduced efficacy due to the huge amount of 

dilution, photolysis and physiochemical association that takes place. The volatility of the 

organic matter also reduces the efficacy of the Active Substance concentration. 

On the other hand because of its high volatility, the ions that are present in the water will 

interfere with the aquatic environment. In this case even if the TRC was measured it would not 

have much significance, when concerned with water quality as it is not tested. 

To meet protocol of toxicity, the unstable PNEC can be calculated with TRC which is lower 

than 1. No significant differences can be distinguished for NOEC amounts from the chronic 

toxicity test between brackish water and seawater. 

7 Risk assessment 

7.1 Safety of ship and crew 

7.1.1 Explosion tests 

When ECS is operated, hydrogen gas is produced and emitted as a result of the electrolysis 

process. Hydrogen gas is known to have the possibility to cause explosions at high 

concentrations. Therefore consideration of the risk assessment of explosion by measuring 

the concentration of hydrogen gases onboard the barge and the M/V STX Yokohama

has taken place. 

Hydrogen is non-toxic and non-poisonous. It will not contaminate groundwater, nor will a 

release of hydrogen contribute to atmospheric pollution. Hydrogen does not create “fumes”. 

The flammability range (volume% in air): 4% to 75%. NTP, OSHA or IARC does not list 

hydrogen gas for carcinogenicity. No adverse ecological effects are expected from hydrogen 

gas. It does not contain any Class I or Class II ozone depleting chemicals. Hydrogen is not 

listed as a marine pollutant by DOT. 

7.1.1.1 On barge test 

Table 7-1 shows that after the ECS operation was finished for land-based test the values of 

hydrogen gas were also measured in four different places, and five different time intervals were 

set to measure the value. The results show a low concentration of hydrogen meaning no risk of 

explosive danger. The safety of the ballast tank has been confirmed without the need of any 

additional ventilation system. 
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Table 7-1. Hydrogen gas concentration on the barge for land-based test (Unit: ppm) 

Surveyed location After 

ECS 

Elapse of 

1 hrs 

Elapse of 

2 hrs 

Elapse of 

12 hrs 

Elapse of 

24 hrs 

Ballast tank area 0.9 0.5 0.2 N.D. N.D. 

Surrounding the ECS N.D. N.D. N.D. N.D. N.D. 

Alongside vessel N.D. N.D. N.D. N.D. N.D. 

Upper regions of vessel N.D. N.D. N.D. N.D. N.D. 

7.1.1.2 Shipboard test 

The values of hydrogen gas were measured in four different places, and five different time 

intervals were determined to measure the value after the ECS operation was finished for the on 

board test. The four places were chosen to be inside of the ballast tank, around the ECS, on the 

deck, and in the crew living quarters. The values of each place were measured since the 

operation finished. Table 7-2 shows a low concentration of hydrogen gas generation and 

therefore no risk of explosive danger. 

Table 7-2. Hydrogen gas concentration on the M/V STX Yokohama for on board test 

(Unit: ppm) 

Surveyed location After 

ECS 

Elapse of 

1 hr 

Elapse of 

2 hrs 

Elapse of 

12 hrs 

Elapse of 

24 hrs 

Ballast tank area 0.8 0.5 0.2 N.D. N.D. 

Surrounding the ECS N.D. N.D. N.D. N.D. N.D. 

Deck N.D. N.D. N.D. N.D. N.D. 

Crew’s quarters N.D. N.D. N.D. N.D. N.D. 

7.1.2 Corrosion effect tests 

Corrosion tests for the control and treated water by ECS were conducted in the ballast tanks and 

pilot tanks using both natural seawater and the pilot tank using artificial seawater of 25ppt of 

sodium chloride. The corrosion effects were compared and tested over 6 months using test 

samples and materials used in the manufacture of the ballast tank. It was found that the 

corrosion rate of the ECS treated tanks group using seawater did not show significant increase 

than that of the control tank group using ECS treated effluent. It can be noted that TRC may 

disinfect the iron-bacteria that causes corrosion. 
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1 month 2 months 3 months 4 months 5 months 6 months 

Fig. 7-1. The corrosion state in test sample with 1 time coating soaked in TRC 0 mg/L 

1 month 2 months 3 months 4 months 5 months 6 months 

Fig. 7-2. The corrosion state in test sample with 1 time coating soaked in TRC 25 mg/L 

1 month 2 months 3 months 4 months 5 months 

Fig. 7-3. The corrosion state in test sample with 1 time coating soaked 1/2 in TRC 25 mg/L 

The result of corrosion degree comparison in test conditions such as control soaking, 

TRC 25 mg/L soaking, and 1/2 soaking (soaked in TRC 25 mg/L for 1 day and out for 1 day) 

appeared in Figures 7-1, 7-2 and 7-3. According to the figures, it was found that the corrosion 

degree in test samples increased in the order of soaking in seawater (control), TRC 25 mg/L 

and 1/2 soaking. 
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7.2 Risks to human health 

7.2.1 Chlorine gas tests 

Chlorine gas generation from ECS operation was measured from different places on board the 

vessel. The short-term exposure limit of chlorine gas is known to be 1ppm (MSDS). 

The measured values of chlorine gas in all of the areas onboard the barge and the 

M/V STX Yokohama are less than 1ppm, meaning that the concentration is at a safe level for 

the crew and that the chlorine gas will dilute safely into the surrounding atmosphere. 

7.2.1.1 On barge test 

As shown in table 7-3, the values of chlorine gas were measured in four different places and at 

five different time intervals after the ECS operation was finished for land-based test. The four 

places were chosen to be inside of the ballast tank, around the ECS, on the port and starboard 

sides of barge, and on the deck of barge and the values from each place were measured since the 

operation finished. 

The results show only very low concentration of chlorine in the ballast tank meaning no risk of 

danger. As the hydrogen gas in the ballast tank is below 1.0ppm, it has been confirmed that 

there is no necessity for any additional ventilation system. 

Table 7-3. Variations of chlorine gas on barge after land-based test (Unit: ppm) 

Surveyed location After 

ECS 

Elapse of 

1 hr 

Elapse of 

2 hrs 

Elapse of 

12 hrs 

Elapse of 

24 hrs 

Ballast tank area 0.9 0.6 0.3 0.1 N.D. 

Surrounding the ECS N.D. N.D. N.D. N.D. N.D. 

Alongside vessel N.D. N.D. N.D. N.D. N.D. 

Upper regions of vessel N.D. N.D. N.D. N.D. N.D. 

7.2.1.2 Shipboard test 

After the ECS operation was finished on the M/V STX Yokohama for the shipboard test the 

concentration of hydrogen gas was measured in four different places, and at 5 different time 

intervals. When the ECS had just finished operation, the value of the chlorine gas inside of the 

ballast tank was measured as 0.7ppm. Table 7-4 shows a low concentration of hydrogen gas 

and therefore no risk to the safety of the ship and crew. 
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Table 7-4. Chlorine gas concentration on the M/V STX Yokohama after 

shipboard test (Unit: ppm) 

Surveyed location After 

ECS 

Elapse of 

1 hrs 

Elapse of 

2 hrs 

Elapse of 

12 hrs 

Elapse of 

24 hrs 

Ballast tank area 0.7 0.5 0.3 0.1 N.D. 

Surrounding the ECS N.D. N.D. N.D. N.D. N.D. 

Alongside vessel N.D. N.D. N.D. N.D. N.D. 

Upper regions of vessel N.D. N.D. N.D. N.D. N.D. 

7.3 Risks to the aquatic environment 

7.3.1 Degradation of TRC 

To predict the degradation rate of TRC in the ballast water tank of the M/V STX Yokohama

after ECS operation, and to compare the degradation rate of TRC in the barge for land-based 

test, the TRC was measured according to time passed. The concentration of TRC in ballast 

water was set to about 10 mg/L. As measuring the TRC concentration in discharging water with 

the passage of time after the ECS operation, TRC was rapidly reduced (Table 7-5). 

Measurement of TRC with the passage of time after the ECS operation was used for the data to 

estimate the degradation rate that satisfies the discharge concentration. A large amount of TRC 

reduction was shown in 1 day after ECS operation. A similar trend of TRC decomposition rate 

was observed in both the barge and M/V STX Yokohama. From the results, it was shown that 

the reducing rate of TRC can be varied depending on the amount and temperature of the 

ballast tank. 

Table 7-5. Typical degradation of TRC in ballast tank 

TRC (mg/L) After ECS 

treated (day) Test barge 

(Sum-jin river)

Test barge 

(Ma-san port) 

M/V STX Yokohama 

(Bu-san port) 

0 9.7 9.9 7.9 

1 4.5 4.8 3.7 

2 2.5 2.9 2.3 

3 1.9 1.9 1.4 

4 1.5 1.6 1.3 

5 1.3 1.5 1.3 

6 1.3 1.5 1.1 

7 1.2 1.4 0.9 

7.3.2 Emission scenario of active substance

Emission scenario was performed to understand the flow condition of seawater including 

TRC when the ballast water is discharged. The emission scenario was done based on the 

condition (spring, neap), amount of discharged water (100%, 50%, 33%), half-life of TRC 

(2 days, 1 day, 1/2 day), and concentration of TRC (30 mg/L, 10 mg/L, 2 mg/L) after the ECS 

was operated in Bu-san port and In-cheon port. 
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When the 50% of discharged water was released with 1/2 of half-life, 2 mg/L of TRC 

concentration, and spring tide in Bu-san port, the diffusion area where the TRC concentration 

decreases to 0.3 mg/L was calculated to be 0.002km2 and the diffusion area where the TRC 

concentration decreases to 0.05 mg/L was calculated to be 0.059km2

.

 When the 100% of 

discharged water was released under the same condition, the diffusion area where the TRC 

concentration decreases to 0.3 mg/L was calculated to be 0.007km2 and the diffusion area where 

the TRC concentration decreases to 0.05 mg/L was calculated to be 0.185km2

. 

When the 100% of discharged water was released with 1/2 of half-life, 1 mg/L of TRC 

concentration, and spring tide in Bu-san port, the diffusion area where the TRC concentration 

decreases to 0.1 mg/L was calculated to be 0.015km2 and the diffusion area where the TRC 

concentration decreases to 0.05 mg/L was calculated to be 0.050km2

.

Predicted dilution concentrations set to be the same condition with the actual discharging, were 

lower than the values that were analysed based on the characteristic of TRC.

7.3.3 PEC/PNEC 

7.3.3.1 PEC calculation

The PEC calculation was obtained according to the Bu-san Port statistics referred to in the 

Emission scenario. From the Korea Ocean Science & Engineering Corporation (KOSEC) data 

the Bu-san port water volume is 207,000,000m3

 and the annual ballast discharge 

is 111,683,505m3

. In the case of ECS the daily ballast discharge is 305,982m3. The ECS 

operates at 10 mg/L and the discharge is set to be at 2 mg/L. From the assumption that it 

takes 24 hours for the TRC concentration to completely mix with the seawater the ballast is 

consequently calculated in standard to the one day PEC discharge amount. Therefore, 

mg L mg L PEC 0.00296 /

207,000,000

305,982 2.0 / = × =

7.3.3.2 PEC/PNEC calculation 

7.3.3.2.1 Brackish water from 3 days after ECS operation 

Three kinds of trophic levels (algae, invertebrate, fish) were examined with treated water for 

chronic toxicity test, and the lowest value of NOEC was 0.8 mg/L among three trophic levels 

and it was shown from algae, so the assessment factor produces PNEC dividing by 100. 

mg L mg L PNEC 0.008 /

100

0.8 / = =

Value of predicted environmental concentration (PEC): 0.00296 mg/L 

Value of no effect on environmental concentration (PNEC): 0.008 mg/L 

0.37

0.008 /

0.00296 / / = = mg L

mg L PEC PNEC

PEC/PNEC is less than 1 so it means it will be safe to the environment. 
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7.3.3.2.2 Seawater from 3 days after ECS operation 

Three kinds of trophic levels (algae, invertebrate, fish) were examined with treated water for 

chronic toxicity test, and the lowest value of NOEC was 0.6 mg/L among three trophic levels 

and it was shown from algae so the assessment factor produces PNEC dividing by 100. 

mg L mg L PNEC 0.006 /

100

0.6 / = =

Value of predicted environmental concentration (PEC): 0.00296 mg/L 

Value of no effect on environmental concentration (PNEC): 0.006 mg/L 

0.49

0.006 /

0.00296 / / = = mg Lmg L PEC PNEC

PEC/PNEC is less than 1 so it means it will be safe to the environment. 

7.3.3.2.3 Brackish water from 5 days after ECS operation 

Three kinds of trophic levels (algae, invertebrate, fish) were examined with treated water for 

chronic toxicity test, and the lowest value of NOEC was 0.5 mg/L among three trophic levels 

and it was shown from algae, so the assessment factor produces PNEC dividing by 100. 

mg L mg L PNEC 0.005 /

100

0.5 / = =

Value of predicted environmental concentration (PEC): 0.00296 mg/L 

Value of no effect on environmental concentration (PNEC): 0.005 mg/L 

0.59

0.005 /

0.00296 / / = = mg Lmg L PEC PNEC

PEC/PNEC is less than 1 so it means it will be safe to the environment. 

7.3.3.2.4 Seawater from 5 days after ECS operation 

Three kinds of trophic levels (algae, invertebrate, fish) were examined with treated water for 

chronic toxicity test, and the lowest value of NOEC was 0.3 mg/L among three trophic levels 

and it was shown from algae, so the assessment factor produces PNEC dividing by 100. 

mg L mg L PNEC 0.003 /

100

0.3 / = =

Value of predicted environmental concentration (PEC): 0.00296 mg/L 

Value of no effect on environmental concentration (PNEC): 0.003 mg/L 

0.99

0.003 /

0.00296 / / = = mg Lmg L PEC PNEC

PEC/PNEC is less than 1 so it means it will be safe to the environment.
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8 Assessment report 

The persistence, bioaccumulation and toxicity were assessed based on reliable biological 

resources on the physicochemical properties and environmental toxicity of the Active Substance 

generated with the electrolysis of seawater through the Electro-Clean System (ECS) from the 

ballast water treated by the Active Substance. The tests for persistence were done under 

simulation test systems in approved laboratory conditions. 

The Active Substance or the relevant chemicals generated from ballast treatment through ECS 

has no persistence or bioaccumulation. Biodegradation tests show the Active Substance and 

relevant chemicals to have little or no half-life and are therefore of no risk to the safety of ship 

and crew (human health), the environment and resources during development and large 

scale testing. 

From the data there are formations of radicals from the electrolysis process. The lives of these 

radicals range from milliseconds to micro-milliseconds and therefore have no risk to the 

environment. Half-life of these radicals is short enough that they will not be a risk to the 

ecosystem of the area in which the ballast water is discharged. 

The data shows the generation of hydrogen and free chlorine gas were generated during the 

electrolyte process. It should be confirmed that residual levels of these substances with in the 

ballast tanks following the treatment process remain with in acceptable limits for crew and 

ship safety. 

The active substances HOCL, OCl-

 are produced from the ECS process and have been 

confirmed to have a very short life span. 

• Shipboard and land-based tests were performed by KORDI with certification 

by KOLAS. 

• The ECS function during land-based test, organism netting, the extraction of 

control/treated water and other preparations for test were all inspected 

by KORDI. 

• The KORDI land-based and shipboard tests for the organism disinfection 

efficacy (L group, S group, bacteria) made use of internationally 

certificated protocol. 

• For the reliance of the tests, the ECS function log data (function location, time, 

navigation information) have been attached. 

• The acute and chronic toxicity tests were all performed in accordance to 

EPA protocol. 

• The organisms for the toxicity tests for the land-based tests were all selected 

from habitation around the Ma-san port and Sum-jin river. 

• The treated water used for the water quality analysis and toxicity tests were 

sampled from ECS operation at the land-based test barge. 
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• The corrosion test was performed in accordance with the protocol presented 

by ASTM. 

• The laboratory of Techcross is a certificated body of DIN EN ISO 9001 quality 

management system and DIN EN ISO 14001 environmental management 

systems, which are certificated by the MSA Certification and accredited by the 

German Association for Accreditation GMBH. 

• All of the toxicity tests were calculated with EPA protocol and SAS statistic 

program for LC50 and NOEC. 

• For further authorization of the analysis of water, the accuracy and precision 

values were calculated using SPSS statistic program.
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