I:\MEPC\57\2-1.doc For reasons of economy, this document is pr inted in a limited number. Delegates are kindly asked to bring their copies to mee tings and not to request additional copies. 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 ORGANI SMS IN BALLAST WATER

Application for Final Approval of a ba llast water management system using Active Substances (Electro-Cle an Electrolytic Disinfection)

Submitted by the Republic of Korea

SUMMARY

Executive summary: This document contains an applica tion for Final Appr oval 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 Activ e 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 whic h make use of Active Substances or preparations containing one or more Active Subs tances shall be approved by the Organization under the Regulation D-3.2 of the Ba llast 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 se ction 6 of the Procedure (G9), the Organization should evaluate the informati on provided in the application.

3 According to BWM.2/Circ.10, a document on th e proposal for approval containing all the non-confidential data related to the respective Ba llast Water Management Systems that make use
of Active Substance should be submitted to ME PC 56 or, if this is not possible, to MEPC 57 not later than 7 September 2007.

4 Republic of Korea has verified the applica tion 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-c onfidential part of the manufact urer’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 conf idential 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 WA TER MANAGEMENT SYSTEM

1 Introduction

The Electro-Clean System (ECS), designed and manufactured by Techcross Inc., is the ballast water management system that has been engineer ed for the disinfection of micro-organisms that would otherwise be indigenous to the aquatic eco system. 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 ap plication 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 leav e any trace, generated during the electrolysis procedur e also disinfect micro-organi sms. Hypochlorite is highly reactive and easily degraded in seawater contai ning both organics and inorganics. The active substance used in the process of ECS and disi nfection by-products do not cause any secondary pollution and is therefore not harm ful 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 le vel 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 treat ed ballast water has proven to satisfy the D-2 standard.

From March to August 2007, toxic ity tests in accordance with th e existing guidelines have been conducted to analyse the impact of treated ba llast water on ecosystems of seawater and of
brackish water. Corrosion tests have been cond ucted 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 avai lability of the electro chemical 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 Paci fic, Singapore, ICBWM 2006 in Singapore, and 2006 Lloyd’s List Conference on Balla st Water Management in London.MEPC 57/2/1
ANNEX Page 2

I:\MEPC\57\2-1.doc The Active Substances are generated during the el ectrolysis process by EC S, when chloride ion
in seawater is oxidized and convert ed into chlorine that is subse quently 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. Th e chemical compounds of reactive chlorine and
other oxidants are called Total Residual Chlorine (TRC) or to tal residual oxidants (TRO). They have been recognized to dest roy micro-organisms instantaneously.

The total residual chlorine conc entration 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 (H F Scientific, Inc.). The CLX measures the TRC concentration in seawater by the DP D (N, N-Diethyl-P-Phenylenediamine) method.

The concentration for Active Substances can be m easured in terms of TRC. From biological efficacy tests, 10 mg/L of TRC is effective en ough 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 concentrati on has been reduced from 30 mg/L to 10 mg/L. From the long-term land-based test results, th e 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, Cl 2 (g) is formed from oxidation of chloride
ion and is dissolved into seawater as follows:

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

Cl 2 (aq) then hydrolyzes, one of the chlorine at oms being oxidized to +1 and the other reduced to -1. This reaction is called dispropo rtionation. The reaction is as follows:

Cl 2 (aq) + H 2 O HOCl + H + + Cl -1 K H = 4 x 10 -4 (2-2)

From Equation (2-2), the hypochl orous acid, HOCl, is formed. The water becomes acidic. If the water is intentionally made acidic, the re action will be driven to the left, producing more
of the chlorine molecule. This condition will th en produce more disinfec ting 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 Cl 2 (aq) and HOCl can be calcu lated. Expressing in the form of equilibrium equation:

KH = 4 x 10 -4 = )] ( [ ] ][ ][ [

2 aq Cl Cl H HOCl

− + (2-4)

Taking logarithms, rearranging and simplifying:

)] [ )] ( [ 2

HOCl aq Cl = 10 {pK H -pH+Log[Cl-]} (2-5)MEPC 57/2/1
ANNEX

Page 3

I:\MEPC\57\2-1.doc Using Equation (2-3), let us calcul ate the distribution of HOCl and OCl - . Note that from previous result, HOCl predominates over Cl 2 (aq) above pH4.0, Cl 2 (aq) being practically zero. Thus above this pH, the distribution of the chlo rine species will simply be for HOCl and OCl -

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

Ka = 10 -7.5 = ] [ ]

][ [

HOCl OCl H − + (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, OCl predominates over all chlorine disinfectant species.

The three species Cl 2 (aq), HOCl, and OCl - are called total free chlorine. Although Cl 2 (aq) is a stronger oxidizer than the ot her 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 ba cterial cell. HOCl can produce oxidation, hydrolysis and deamination reactions with a va riety of chemical substrates, and produces physiological lesions that may aff ect several cellu lar 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, su ggesting that chlorine causes physiological damage primarily to the bacterial cell membranes (Camper & McFeters, 1979; Haas & Engelbr echt, 1980; Albrich, McCarthy & Hurst, 1981).

In addition, chlorination can kill microbes by di srupting metaboli sm and protein synthesis, or by modifying purine and pyrimidine ba ses and thus causi ng 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 un its, the electrolysis module, and control systems. The multi-function relay mon itors 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 Page 4

I:\MEPC\57\2-1.doc 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 init ial 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 th e most effective disinfection. During inballasting, the Electro-C lean System continuously contro ls 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 th e appropriate quantity of DC power to the electrolysis module, and the cooler discharges heat generated fr om 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 c ontrol 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 ther e are variances depending on the pr operties 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 rectifie r 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 concentra tion, 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 substa nce material generated from electrolysis.
Generation of the active substance TRC is contro lled 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 fact ors 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 therefor e 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 connec tion to the ECS control system. However, maximum TRC concentration generated by ECS can be controlled precisely.MEPC 57/2/1
ANNEX

Page 5

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 generati on and measures electric curren t 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 op timum current density is determined on the basis of salinity, flow and cont rol of the disinfection level.

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

.4 Revise the salinity-current capacity rela tional 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 concentr ation 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 SCIENTIF IC INC.) system, which is then sent to the main control PC for real time monitoring by th e 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 th e operation of ECS and records, reports, and prints all ballast operating data, as well as provide alarms. Th e PC is operated with Windows based program allowing user-friendly operation. When the balla st 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 activ e substances reacted with organic and inorganic species, micro-organisms are disinfected and T RC 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 Page 6

I:\MEPC\57\2-1.doc Table 3-1. TRC degradation of ECS treated wa ter 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 mu ltifunctional relay (HIMAP).

3.2.2 Control unit

z Main Features

• The Control PC collects and contro ls all data through the RTU and other components by communications.

• The RTU receives input from the se nsors 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 r ectifier to stabilize its performance.

3.2.4 Electrolyzer

z Electrolysis unit consists of multiple el ectrodes and electrolysis module chamber.
Electrode module is inserted into module chamber.

z Main features

• Eliminates micro-organisms, bact eria, 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

Page 7

I:\MEPC\57\2-1.doc 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) fo r ISO/IEC 17025 in field of aquatic organisms and all disinfection efficacy tests are condu cted 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 th e general requirements of ISO/IEC 17025, general requirements for the competence of testing and calibration laboratories and specific technica l requirements of each field.

The efficacy of ballast water management systems, which make use of active substances possible, was evaluated by administration in accor dance with guidelines for approval of ballast water management systems (G8). The guidelines (G8) include general re quirements 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 a pproval 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, ecologica l efficacy of ECS was proved. Each of four
test tanks has 200m 3 of volume (Table 4-1). All pipes a nd valves in each test tanks were installed and designed based on th e regulation, and the four 500m 3 /h ballast pumps were installed. For sampling, four ta nks for treated water, each has 2m 3 in volume, and four controlled water tanks with pipeli nes and valves were installed.

Table 4-1. Barge for ECS la nd-based test specification

Item Specification

Name/Type ELECTRO-CLEAN/Barge

Gross Tonnage 203m 3

Dimensions Length 34.31m Width 13.40m Depth 2.4m

Builder Daeun Shipyard

Launching

Date May 1, 2006MEPC 57/2/1
ANNEX Page 8

I:\MEPC\57\2-1.doc 4.2.2 Result of land-based test

The land-based tests were performed at two differ ent sites with more than 10 ppt difference in salinity according to the G-8 guidelines. The loca tions 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 (sal ine 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 15 th April to 30 th May 2007 and a total of 5 repetitions were performed. The tests in Sum-jin rive r for brackish water commenced from 1 st June
to 25 th 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 th e Korean brackish water, between 10~50 μm 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 8,306m 3

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 3 rd February to 30 th July 2007 (Total of 24 weeks).MEPC 57/2/1
ANNEX

Page 9

I:\MEPC\57\2-1.doc The operation conditions of ECS were controlle d 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 T RC) were seen to be very
low. In the case of OH - , which has a very short lifetime dur ing ECS operation, and also as the ballast water flows quickly through the ECS, ther e was no notable effect on disinfection in the ballast water. The radicals generated by electro lysis decompose easily without sedimentation. Electric potential is an instant process that ta kes 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 mi cro-organisms in seawat er containing various concentrations of suspended solids and organi c 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 acti ve substances from electrolysis of water, due to the important role of electrical potential on disinfection of livin g organisms in ballast water.
But the identification of active substance as a ki nd 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 OCl Structural 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 st abilizer (cyanuric acid).MEPC 57/2/1
ANNEX Page 10

I:\MEPC\57\2-1.doc 5.1.2 Identification of by-products

Chlorine is an effective disinfectant for reducin g 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 ch lorine and other substances present in the
effluent water. TRC includ es free residual chlorine of undissociated and dissociated hypochlorite when chlorine is dissolved in water, plus co mbined residual chlorine of chloramines formed by reacting with ammonia. “CBPs” refer to chlorinated organic compounds (or total organic halogen) form ed by the action of chlorine on the total organi c carbon fraction of treated water. The two largest identified fr actions of CBPs mostly fo rmed by chlorination are trihalomethanes (THMs) and haloacetic acids (HAAs).

Table 5-2 and 5-3 show the analytical results of disinfection by-product s from electrolysis of brackish and seawater by EC S operation for the production of 10 mg/L of TRC. The concentration of disinfection by-products ca n vary compared to th e raw water condition, half life and sedimentation, a nd 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. < 0.002MEPC 57/2/1
ANNEX Page 11

I:\MEPC\57\2-1.doc 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-produc ts was performed. The cont rol and treated samples with ECS were collected in Ma-san port (28~30ppt) a nd 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 ha ve 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 onl y four by-products, dibromochl oromethane, tribromomethane,
dibromoacetic acid and tribromoacetic acid that is produced by ECS. The informations of these by-products are shown in tabl e-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 ClCHBr 2

Structural formula

Purity of technical material and identification of impurities 99% of
dibromochloromethane Stabilizers or necessary additives N.A.MEPC 57/2/1
ANNEX Page 12

I:\MEPC\57\2-1.doc 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 CHB 3

Structural formula

Purity of technical material and iden tification 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 C 2 H 2 Br 2 O 2 Structural formula

Purity of technical material and identification of impurities 99% of dibromoacetic acid

Stabilizers or necessary additives Stab le 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 CBr 3 COOH
Structural formula

Purity of technical material and identification of impurities 99% of tribromoacetic acid

Stabilizers or necessary additives Stab le at room temperature in closed containers under normal storage and handling
conditions without stabilizer.MEPC 57/2/1
ANNEX Page 13

I:\MEPC\57\2-1.doc 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 producti on of endocrine disruption

No report on production of endocrine disruption of hypochlorite is availa ble 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 s odium hypochlorite with –3.42 (EPI SuitTM, U.S.EPA v3.20), the possibility of predicted Bi oavailability/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. B ecause of very low Log Pow value of sodium hypochlorite, the adverse effect on food web should be insignificant.MEPC 57/2/1
ANNEX Page 14

I:\MEPC\57\2-1.doc 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 t oxicity 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. , 1984MEPC 57/2/1
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I:\MEPC\57\2-1.doc 5.2.2.5 Development and reproductive toxicity

Table 5-14. The development and reproducti ve 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/mut agenicity 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 con centration, 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 w ill be reduced 3~4 times by sunlight. Half life
of more than 20% available ch lorine solution will be reducedby 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 v3.20MEPC 57/2/1
ANNEX Page 16

I:\MEPC\57\2-1.doc 5.2.3.3 Persistence and identifi cation 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 hy pochlorite species (HOCl, OCl), high molecular weight chlorinated compounds form in a first st ep that is followed by the cleavage of benzene rings into trihalomethanes and haloacetic acids . Sodium hypochlorite tr eated 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 aff ect physical wildlife
and benthic habitats.

5.2.3.6 Potential residues in seafoods

No report on potential residues in seafood of hypochlorite is av ailable. 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 chemic al 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/cm 3 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 us ed for the remnant
disinfection of drinkable water IUCLIDMEPC 57/2/1
ANNEX Page 17

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

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 me asuring 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 Cl 2 Reference Standard Methods for the Examina tion of Water and Waste Water, 18th edition, American Public Health Association (APHA),

5.2.5.2 Risk characterization

Table 5-20. Acute aquatic toxici ty 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 dibromochlorom ethane on aquatic organisms

5.3.1.1 Acute aquatic toxicity data

Table 5-20. Acute aquatic toxici ty 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 toxi city of dibromochloromethane

Species LC50 or NOEC (mg/l/duration) Reference
Fish Cyprinus carpio LC50: 34 mg/L (NR d) Trns.Am.Fish.Soc.MEPC 57/2/1
ANNEX Page 18

I:\MEPC\57\2-1.doc 5.3.1.3 Information on endocrine disruption

Several studies have examined the potential of dibromochloromethane to induce histological alterations in endocrine glands following longe r-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 gava ge 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 observe d in rats given gavage doses of 160 mg/kg/day for 7 days. However, a decrease in levels result ed from doses of 310 mg/kg/day (Potter et al . 1996).

5.3.1.4 Sediment toxicity

Both tribromomethane and dibromochloromethane ar e 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 chemi cal 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 concentra tion 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. Theref ore, possibility of sedimentation in food web as the level goes up is predicted very low. Di bromochloromethane 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 ., 1980MEPC 57/2/1
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I:\MEPC\57\2-1.doc 5.3.2.2 Corrosion/Irritation

Table 5-23. The eye and skin irri tation 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 sensi tization is given to dibromochl oromethane. This is, however, primarily due to lack of information, and sk in contact with dibromochloromethane should
be minimized.

5.3.2.4 Repeated-dose toxicity

Table 5-24. The repeated-dose toxici ty test of dibr omochloromethane

Exposure Route Eating Exposure Duration 90 days Exposure dose 0,50,100,and 200 mg Species Rat

Method
- Results No changes were found in mo rtality, 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 di bromochloromethane

Exposure Route GO (gavage oil) Exposure Duration 9 days Exposure dose 200 mg/kg/day Species Rat

Method
- Results No alternation in the nu mber of resorption site s, fetuses per litter, fetal body weights fetal gross malfor mations, or skeletal or visceral
anomalies were found.
NOAEL 200 mg/kg/day

NOEL N.A.
Reference Ruddick et al . (1983)MEPC 57/2/1
ANNEX Page 20

I:\MEPC\57\2-1.doc 5.3.2.6 Carcinogenicity/Mutagenicity

Table 5-26. The carcinogenicity/mutageni city test of dibr omochloromethane

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 degrad ation 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 46 μ g/L to
3 μ g/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 Ko c 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 identifica tion of main metabolites

Because of low Log Pow and no bioavailability, there was no report on persistence and
identification of main metabol ites in dibromochloromethane.MEPC 57/2/1
ANNEX Page 21

I:\MEPC\57\2-1.doc 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/m 3 at 20°C) is higher than density of seawater (1025kg/m 3 ), and dibromochloromethane is sligh tly soluble with 2.7 x 10 mg/L of
water solubility at 20 ° C. Therefore, it may have potenti al 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 se diment, 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 dibr omochloromethane

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/cm 3 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) 2.7x10 3 mg/L (20 ° C) Horvath 1982; Heikes 1987

5.3.5 Other information

5.3.5.1 Analytical methods for me asuring 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 μ g/kg/Accuracy (percent recovery) : 94

Reference EPA 1986aMEPC 57/2/1
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I:\MEPC\57\2-1.doc 5.3.5.2 Risk characterization

Table 5-31. Some indices for risk char acterization 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 tribromometh ane 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 consiste ntly found. The observed endocri ne effects included enlarged thyroid gland in rats administered a lethal dose of 800 mg/kg/day for 14 days (NTP 1989a), decreased thyroid follicular si ze 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 year s (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 fo r 7 days (Potter et al. 1996).MEPC 57/2/1
ANNEX Page 23

I:\MEPC\57\2-1.doc 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 broke n down by bacteria, but the speed of this process is not known.

According to CITI (1992) and Sangster (1994), th e value of Log Pow is 2.4, which is smaller
than the indicated value of bioaccumulation whic h 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 sm aller 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 sm aller 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 i rritation 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 tribro momethane should be minimized.MEPC 57/2/1
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I:\MEPC\57\2-1.doc 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 histopathologica l 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 reproducti ve 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 skelet al 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 evalua te the contribution of these pathways to the genotoxicity and carcinogenici ty of tribromomethane.

Table 5-38. The carcinogenicity/mutage nicity 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 1998MEPC 57/2/1
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I:\MEPC\57\2-1.doc 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 58 μ g/L
to <1 μ g/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 identifica tion of main metabolites

Because of low Log Pow and no bioavailability, there was no report on persistence and
identification of main meta bolites in tribromomethane.

5.4.3.4 Reaction with organic matter

No report on reaction with organic matte r of tribromomethane is available.

5.4.3.5 Potential physical affects on wildlife and benthic habitats

Density of tribro momethane (2890kg/m 3 at 20°C) is higher than density of seawater (1025kg/m 3 ), and tribromomethane is slightly soluble with 3.1 x 10 mg/L of water solubility at 25°C. Therefore, it may have potential phy sical 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 sediment ation, and the potential residues in seafood are predicted as low.MEPC 57/2/1
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I:\MEPC\57\2-1.doc 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/cm 3 Lide, 2000 Vapour pressure (25 °C; mmH g) 5.34mmHg EPI Suit V 3.20 Vapour density (air = 1) 8.7 IARC 1991a, 1991b

Water solubility 3.10x10 3 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 co ncentration at environmentally relevant
concentrations

Table 5-42. Analytical methods

Method GC-HSD (gas chromatography – halide specific detector) Applicability Contaminated soil Sensitivity Sample detection limit : 2 μ g/kg/Accuracy (percent recovery) : 96

Reference EPA 1986a

5.4.5.2 Risk characterization

Table 5-43. Some indices for risk ch aracterization 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 chroni c aquatic toxicity data of di bromoacetic acid is available.MEPC 57/2/1
ANNEX Page 27

I:\MEPC\57\2-1.doc 5.5.1.3 Information on endocrine disruption

No report on production of endoc rine 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 di bromoacetic 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 Bi oavailability/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.MEPC 57/2/1
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I:\MEPC\57\2-1.doc 5.5.2.4 Repeated-dose toxicity

Table 5-45. The repeated-dose toxici ty 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 we ights, 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 malf ormation 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/mutageni city 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, 2003cMEPC 57/2/1
ANNEX Page 29

I:\MEPC\57\2-1.doc 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 identifi cation 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 matte r of dibromoacetic acid is available.

5.5.3.5 Potential physical affects on wildlife and benthic habitats

Density of dibromoacetic acid (2450kg/m 3 at 20°C) is higher than density of seawater (1025kg/m 3 ), and dibromoacetic acid is s lightly soluble with 2.214 x 10 4 mg/L of water solubility at 20°C. Therefore, it might ha ve potential physical effects on wildlife and
benthic habits.

5.5.3.6 Potential residues in seafood

No report on potential residues in seafood of di bromoacetic acid is available. However, dibromoacetic acid has low possibility of sedi mentation, and the poten tial residues in seafood are predicted as low.MEPC 57/2/1
ANNEX Page 30

I:\MEPC\57\2-1.doc 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 10 4 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 co ncentration 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 char acterization 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.MEPC 57/2/1
ANNEX Page 31

I:\MEPC\57\2-1.doc 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 valu e 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/Bi omagnification is cons idered 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 aci d. 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 sl ight and inconsistent decrease in water consumption in th e 400 mg/L animals.

Reference NTP Study Number: RDGT94009MEPC 57/2/1
ANNEX Page 32

I:\MEPC\57\2-1.doc 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 fi ndings were unremarkable.

Reference NTP Study Number: RDGT94009

5.6.2.6 Carcinogenicity/Mutagenicity

Table 5-55. The carcinogenicity/mutageni city 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 with in water distribution sy stems is altogether lacking. Thus, in situ studies of HAA biodegradation (including those HAAs not studied herein) in natural waters and dr inking water distribution systems ar e 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 V3.20MEPC 57/2/1
ANNEX Page 33

I:\MEPC\57\2-1.doc 5.6.3.3 Persistence and identifi cation 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/m 3 at 20°C) is higher than density of seawater (1025kg/m 3 ), and tribromoacetic acid is s lightly soluble with 1.199 x 10 4 mg/L of water solubility at 25°C. Therefore, it might ha ve potential physical affects on wildlife and
benthic habits.

5.6.3.6 Potential residues in seafood

No report on potential residues in seafood of trib romoacetic acid is available. However, tribromoacetic acid has low possibility of sedi ment, 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 10 4 at 25 ° C US EPA Mabey et al , 1985

5.6.5 Other information

5.6.5.1 Analytical methods for me asuring 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 552.2MEPC 57/2/1
ANNEX Page 34

I:\MEPC\57\2-1.doc 5.6.5.2 Risk characterization

Table 5-60. Some indices for risk charac terization 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 discharg ing ballast water after ECS opera tion were done by the Kyung-hee University. The laboratory of the Kyung-hee University conducte d the tests according to the standard procedures for toxi city tests of US EPA Intern ational standard procedures. The laboratory was established and maintained th e 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 dilu tion with culture media or raw water for acute (LC 50 – 96hrs) and some chronic toxicity tests acco rding 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 we re collected from Sum-jin river (18ppt) and seawater from Ma-san port (30ppt). The meas ured 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 fr om 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 waterMEPC 57/2/1
ANNEX Page 35

I:\MEPC\57\2-1.doc 6.2.1.2 Chronic toxicity test

Table 6-2. Chronic toxicity test with t reated 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 treate d 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 trea ted 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 waterMEPC 57/2/1
ANNEX Page 36

I:\MEPC\57\2-1.doc 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 fr om 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 t reated 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 treate d 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 trea ted 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 waterMEPC 57/2/1
ANNEX Page 37

I:\MEPC\57\2-1.doc 6.3 Test results

The result of the toxicity test of discharg ing water with different storing times after ECS operation in seawater and brackish water, s how that the discharged water which had been stored for three days showed highe r toxicity than that of stored for five days. Because of the
unstable characteristics of oxidant s 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 deficien t 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 associa tion 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 PN EC can be calculated with TRC which is lower than 1. No significant differe nces can be distinguished fo r NOEC amounts from the chronic toxicity test between brac kish 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 th e possibility to cause explosions at high
concentrations. Therefore consideration of th e 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. Hydr ogen does not crea te “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 Cl ass 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 ta nk has been confirmed without the need of any additional ventilation system.MEPC 57/2/1
ANNEX Page 38

I:\MEPC\57\2-1.doc 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 f our different places, a nd five different time
intervals were determined to measure the valu e 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 va lues of each place were measured since the operation finished. Table 7-2 shows a low concentration of hydroge n 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 p ilot tank using artificia l 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 usi ng seawater did not show significant increase than that of the control tank gr oup using ECS treated effluent. It can be noted that TRC may
disinfect the iron-bacteria that causes corrosion.MEPC 57/2/1
ANNEX Page 39

I:\MEPC\57\2-1.doc 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 coat ing 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 a nd 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.MEPC 57/2/1
ANNEX Page 40

I:\MEPC\57\2-1.doc 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 ch lorine 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, meani ng that the concentration is at a safe level for the crew and that the chlorine gas will di lute safely into the surrounding atmosphere.

7.2.1.1 On barge test

As shown in table 7-3, the values of chlorine ga s were measured in four different places and at five different time intervals after the ECS operati on was finished for land-based test. The four places were chosen to be inside of the ballas t tank, around the ECS, on the port and starboard sides of barge, and on the deck of barge and th e 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 1.0pp m, 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 operati on, 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 sa fety of the ship and crew.MEPC 57/2/1
ANNEX Page 41

I:\MEPC\57\2-1.doc 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 degrada tion rate of TRC in the barge for land-based test, the TRC was measured according to time pa ssed. 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 re duced (Table 7-5). Measurement of TRC with the passage of time af ter the ECS operation was used for the data to estimate the degradation rate that satisfies the discharge concentr ation. 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 de pending 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.MEPC 57/2/1
ANNEX Page 42

I:\MEPC\57\2-1.doc When the 50% of discharged water was releas ed 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 wa s calculated to be 0.002km 2 and the diffusion area where the TRC concentration decreases to 0.05 mg /L was calculated to be 0.059km 2

. 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 0.007km 2 and the diffusion area where
the TRC concentration decreases to 0. 05 mg/L was calculated to be 0.185km 2

. When the 100% of discharged water was releas ed 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 wa s calculated to be 0.015km 2 and the diffusion area where the TRC concentration decreases to 0.05 mg /L was calculated to be 0.050km 2

.

Predicted dilution concentrations set to be the sa me condition with the actual discharging, were lower than the values that were analys ed based on the characteristic of TRC.

7.3.3 PEC/PNEC

7.3.3.1 PEC calculation

The PEC calculation was obtained according to th e Bu-san Port statistics referred to in the
Emission scenario. From the Korea Ocean Scie nce & Engineering Corporation (KOSEC) data the Bu-san port water volume is 207,000,000m 3 and the annual ballast discharge is 111,683,505m 3 . In the case of ECS the daily ballast discharge is 305,982m 3 . The ECS operates at 10 mg/L and the disc harge 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 th e one day PEC discharge amount. Therefore,

L mg L mg PEC / 00296

. 0 000

, 000

, 207 / 0

. 2 982

, 305

= ×

=

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 assessm ent factor produces PNEC dividing by 100.

L mg L mg PNEC / 008

. 0 100 / 8

. 0

= =

Value of predicted environmental co ncentration (PEC): 0.00296 mg/L
Value of no effect on environmental concentration (PNEC): 0.008 mg/L

37

. 0 / 008

. 0 / 00296

. 0 / = = L mg L

mg PNEC PEC

PEC/PNEC is less than 1 so it means it will be safe to the environment.MEPC 57/2/1
ANNEX Page 43

I:\MEPC\57\2-1.doc 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 assessm ent factor produces PNEC dividing by 100.

L mg L mg PNEC / 006

. 0 100 / 6

. 0

= =

Value of predicted environmental co ncentration (PEC): 0.00296 mg/L
Value of no effect on environmental concentration (PNEC): 0.006 mg/L

49

. 0 / 006

. 0 / 00296

. 0 / = = L mg L

mg PNEC PEC

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 assessm ent factor produces PNEC dividing by 100.

L mg L mg PNEC / 005

. 0 100 / 5

. 0

= =

Value of predicted environmental co ncentration (PEC): 0.00296 mg/L
Value of no effect on environmental concentration (PNEC): 0.005 mg/L

59

. 0 / 005

. 0 / 00296

. 0 / = = L mg L

mg PNEC PEC

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 assessm ent factor produces PNEC dividing by 100.

L mg L mg PNEC / 003

. 0 100 / 3

. 0

= =

Value of predicted environmental co ncentration (PEC): 0.00296 mg/L
Value of no effect on environmental concentration (PNEC): 0.003 mg/L

99

. 0 / 003

. 0 / 00296

. 0 / = = L mg L

mg PNEC PEC

PEC/PNEC is less than 1 so it means it will be safe to the environment.MEPC 57/2/1
ANNEX Page 44

I:\MEPC\57\2-1.doc 8 Assessment report

The persistence, bioaccumulation and toxicity were assessed based on reliable biological resources on the physicochemical properties and e nvironmental 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 chemical s generated from ballast treatment through ECS has no persistence or bioaccumulation. Biodegr adation 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), th e environment and resources during development and large scale testing.

From the data there are formations of radicals from the electrolys is process. The lives of these radicals range from milliseconds to micro-m illiseconds and therefore have no risk to the
environment. Half-life of these radicals is s hort enough that they will not be a risk to the ecosystem of the area in which th e 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 prepar ations 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 (func tion location, time, navigation information) have been attached.

• The acute and chronic toxicity te sts were all performed in accordance to EPA protocol.

• The organisms for the toxicity tests fo r 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 qua lity analysis and toxicity tests were sampled from ECS operation at th e land-based test barge.MEPC 57/2/1
ANNEX Page 45

I:\MEPC\57\2-1.doc • The corrosion test was performed in accordance with the protocol presented by ASTM.

• The laboratory of Techcross is a cer tificated 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 calcul ated with EPA protoc ol and SAS statistic program for LC50 and NOEC.

• For further authorization of the analys is of water, the accuracy and precision
values were calculated us ing SPSS statistic program.MEPC 57/2/1
ANNEX Page 46

I:\MEPC\57\2-1.doc 9 References

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