CO-OPERATIVE PROGRAMME
FOR
MONITORING
AND
EVALUATION OF THE LONG
RANGE TRANSMISSION OF
AIR POLLUTANTS IN EUROPE
MSC-E
EMEP
Meteorological Synthesizing
Centre - East
BELARUSIAN CONTRIBUTION
ANNUAL REPORT 2002
Minsk - Moscow, January 2003
Institute for Problems of Natural Resources
Use & Ecology, National Academy of
Sciences of Belarus
10, Staroborysovski tract Minsk, 220114
Belarus
Meteorological Synthesizing Centre - East
Arch. Vlasov str., 51
Moscow, 117 393
Russia
Tel.: +375 17 264 23 12
Fax: +375 17 264 24 13
Tel.: + 7 095 128 90 98
Fax: + 7 095 125 24 09
Preparation of additions and refinements to the EMEP/CORINAIR
Atmospheric Emission Inventory Guidebook regarding heavy
metals in view of peculiarities of the CIS countries technologies
S.Kakareka, T.Kukharchyk, V.Khomich
Preface
PREFACE
Since 1996 by the Institute for Problems of Natural Resources Use and Ecology of National
Academy of Sciences of Belarus as the national contribution to EMEP of Belarus a few projects
directed onto the methodological provision of heavy metals and POPs emission inventory
improvement in Former Soviet Union countries on the basis of the EMEP methodology have
been done. Works have been fulfilled under the supervision of the MSC-East of EMEP.
Materials and data of mentioned projects were used in preparation of certain Guidebook chapters
(2nd, 3d edition), and also by experts of some countries in preparation of national emission data.
Taking into account the interest stressed to such works, scantiness of information on heavy
metals emission from the countries of the former USSR, after consultations with the MSC-E
specialists we suggested a project which proceed works started 1996. This project is aimed at the
further improvement of EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
regarding heavy metals in view of peculiarities of the CIS countries technologies with the final
purpose of HM inventory improvement in these countries. Its fulfilment will be a contribution inkind of the Republic of Belarus into the EMEP for 2002; its fulfillment as a national contribution
to EMEP in-kind was approved by the TFEIP Meeting (May 2002, Cordoba) and by EMEP
Steering Body.
Description of the project
Title:
Preparation of additions and refinements to the EMEP/CORINAIR Atmospheric
Emission Inventory Guidebook regarding heavy metals emission in view of peculiarities
of the CIS countries technologies
Goals:
-
Promotion of the Guidebook methodology usage in the FSU countries
Improvement of the Guidebook in view of peculiarities of the FSU specificity
Tasks:
-
Summarizing of test study results
Additional investigation of selected activities (especially, small combustion) for
improvement of emission factors and methodological approaches to emission inventory.
Preparation of additions (insertions) to the EMEP/CORINAIR Atmospheric Emission
Inventory Guidebook
Work-plan for 2002 was approved by the EMEP Experts Meeting (17 January 2002, Moscow).
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Preface
Work-plan for the second stage of the project
Activity
Terms
1. Analysis of the EMEP/CORINAIR Atmospheric Emission Inventory I - III
Guidebook in view of HM data
2. Further research and analysis of selected technologies for the improvement IV-V
of HM emission factors and procedures of HM emission inventory
3. Additional investigation of selected activities (e.g. small combustion) for VI-VIII
improvement of emission factors and methodological approaches to emission
inventory
4. Preparation of insertions to the EMEP/CORINAIR Atmospheric Emission VIII-IX
Inventory Guidebook regarding HM emission
5. Preparation of the report
X-XII
Budget for the project (financial statement) see in the Annex.
This year report contains the description of methodology of work and results obtained in 2002,
including:
• Materials for inclusion or usage for preparation of the future releases of the
EMEP/CORINAIR Atmospheric Emission Inventory Guidebook.
• New experimental data on HM emission; main attention was paid onto testing of HM
emission.
Experimental researches, analysis of literature sources, investigation of technological
peculiarities of the Former USSR countries made possible to prepare additions and materials for
inclusion to the Guidebook. Special attention was paid onto source categories which are not
considered in the Guidebook yet (stationary fuel combustion – boilers <50 МWt), or slightly
considered (open burning sources).
For the convenience of the usage results are given in the form of the Guidebook chapter sections;
in the annexes additional material is included.
The project was accomplishment in the Institute for Problems of Use of Natural Resources and
Ecology of the National Academy of Sciences of Belarus (IPUNRE NAS). Specialists from
some other research institutes of Belarus (Belarusian State Polytechnical Academy, BELNIZ
ECOLOGY, industry and agricultural experts as well as experts on emissions from countries of
the FSU were recruited also.
Supervisor of the project –Dr. Sergey Kakareka.
List of authors:
Leading Research Scientist Dr. S.Kakareka
Senior Research Scientist Dr. T.Kukharchyk
Head of the Laboratory Dr. V.Khomich
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In data collection and processing research scientists of IPUNRE V. Chuduk, E.Makaeva took
part. Chemical analyses have been done by Dr. S. Zuj. Report was translated into English by
T.Vashkevich under the editorship of S.Kakareka.
Acknowledgements
For report preparation we used consultations of a great number of specialists from a lot of
institutions, organizations and enterprises of Belarus. We particularly appreciative to Dr.
F.Rozanova (SRPI Energoprom), Dr. N.Lysukho (BELNIZ Ecology), to specialists on boiler
units from PROMATOMNADZOR.
We express our gratitude to the MSC-East of EMEP, SRI Atmosphere and Ministry of Natural
Resources and Environmental Protection of the Republic of Belarus, TFEIP members, all
national experts on emissions for the helpful assistance and support of our work.
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Preface
ACRONYMS AND ABBREVIATIONS
EPA – Environmental Protection Agency (USA)
HM – Heavy Metals
MPC - Maximum Permissible Concentration
PM – Particulate Matter
TSP – Total Suspended Particulate
µg, mkg - microgramme (10-6 gramme)
mg - miligramme (10-3gramme)
kg - kilogramme (103 gramme)
t - tonne (106 gramme)
mkg/kg - microgramme/kilogramme
mg/kg - miligramme/kilogramme
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CONTENTS
ADDITIONS TO THE EMEP/CORINAIR ATMOSPHERIC EMISSION
INVENTORY GUIDEBOOK………………………………………………………….
8
1. SMALL COMBUSTION INSTALLATIONS (DRAFT SECTIONS)…………
2. DEFAULT EMISSION FACTORS TABLES …………………………………
8
18
ANNEXES……………………………………………………………………………….
1. OBJECTS AND METHODOLOGY OF HEAVY METALS EMISSION
TESTING …………………………………………………………………………….
1.1. Processes and Installations Studied in 2002…………………………………..
1.2. Methodology of Emission Sources Testing…………………………………...
1.3. Heavy Metals Analytical Determination……………………………………..
25
25
2. RESULTS OF HEAVY METAL EMISSIONS TESTING…………………….
29
2.1. Solid Fuels Combustion in Small Installations Testing……………………….
2.2. Heavy Metals Content in Emissions from Open Burning Processes………….
29
36
3. MATERIALS TO THE EMEP/CORINAIR ATMOSPHERIC EMISSION
INVENTORY GUIDEBOOK REGARDING HEAVY METALS EMISSION…
38
3. 1 Solid Fuel for Small Combustion Description………………………………..
3.2. Compilation of Heavy Metal Emission Factors for Small Combustion………
38
40
REFERENCES.......................................................................………..............................
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ADDITIONS TO THE EMEP/CORINAIR ATMOSPHERIC EMISSION
INVENTORY GUIDEBOOK
1. SMALL COMBUSTION INSTALLATIONS (DRAFT SECTIONS)
SOURCE ACTIVITY TITLE:
SMALL COMBUSTION INSTALLATIONS
NFR CODE: 1A4a; 1A4bi; 1A4cii; 1A5a and small installations in 1A1a
1.
ACTIVITES INCLUDED
This chapter covers emission from fuel combustion in small and medium boilers and domestic
furnaces.
2.
CONTRIBUTION TO TOTAL EMISSIONS
Input of small combustion installations into total emission vary depending from pollutant and
country. Thus in the global scope dioxins emissions from small combustion sources makes up to
3%, in some countries – up to 58% (Dioxin and Furan Inventories…, 1999). In Belarus small
combustion sources provides about 40% of total dioxins emissions, and about 80% of indicator
PAH emission.
Contribution of fuel combustion in commercial, residential and other sectors (SNAP 02) to total
heavy metals emission in Europe in 1990 was for As 12.4%, for Cd 15.9% and for Hg 27.8%
(Berdowski at al., 1997).
3
GENERAL
3.1
Description
This source category includes combustion systems of small and medium power capacity
designed for heat, steam or hot water production in various sectors: industry, agriculture,
municipal, domestic etc.
3.2
Definitions
Fireplace: simple stove which includes combustion chamber and chimney.
Stove (residential furnace, household stove): arrangement for solid fuel combustion (first of all
wood) in houses.
Boiler: leak-proof vessels for generation of hot water or steam pressure higher than atmospheric.
Steam boiler: leak-proof vessels for generation of steam pressure higher than atmospheric.
Hot-water boiler: leak-proof vessels for generation of hot water pressure higher than
atmospheric.
Chamber (furnace, fire-chamber): an enclosed space provided for the combustion of fuel.
Chimney: brick, metal or concrete stack.
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Windbox: a chamber below the grate or surrounding a burner, through which air under pressure
is supplied for combustion of the fuel.
3.3
Techniques
In general small combustion devices can be divided into the next main groups:
-installations close to open combustion (from this category fireplaces are most common in
Europe);
-installations withous heat-transfer (furnaces, ovens, stoves);
-installations with heat-transfer (mainly water or steam) – various types of boilers.
Small combustion devices are very different in design. Most specific are solid fuel burning
systems; liquid and gaseous fueled installation are often can be fueled by both these types of fuel
(with some reequipment).
a.Fireplaces
Fireplaces are used primary for aesthetic effects and secondary as supplemental heating sources
in houses and other dwellings. Wood is the most common fuel for fireplaces, but coal and
densified wood "logs" may also be burned. The user intermittently adds fuel to the fire by hand.
In common fireplaces are very simple in design and consists of combustion chamber and
chimney.
Fireplaces can be divided into 2 broad categories:
• masonry (generally brick and/or stone, assembled on site, and integral to a structure) and
• prefabricated (usually metal, installed on site as a package with appropriate duct work).
Masonry fireplaces typically have large fixed openings to the fire bed and have dampers above
the combustion area in the chimney to limit room air and heat losses when the fireplace is not
being used. Some masonry fireplaces are designed or retrofitted with doors and louvers to reduce
the intake of combustion air during use.
Prefabricated fireplaces are commonly equipped with louvers and glass doors to reduce the
intake of combustion air, and some are surrounded by ducts through which floor level air is
drawn by natural convection, heated, and returned to the room. Some of these units are equipped
with close-fitting doors and have operating and combustion characteristics similar to wood
stoves.
Masonry fireplaces usually heat a room by radiation, with a significant fraction of the
combustion heat lost in the exhaust gases and through fireplace walls. Moreover, some of the
radiant heat entering the room goes toward warming the air that is pulled into the residence to
make up for that drawn up the chimney. The net effect is that masonry fireplaces are usually
inefficient heating devices. According to (Artjushenko, 1985), 80-90% heat go out into chimney.
Indeed, in cases where combustion is poor, where the outside air is cold, or where the fire is
allowed to smolder (thus drawing air into a residence without producing appreciable radiant heat
energy), a net heat loss may occur in a residence using a fireplace.
b. Stoves (furnaces)
Generally stoves are simple devices and include following main systems: combustion chamber,
windbox, chimney and convectional system. Mainly stoves are fueled with wood (biomass).
They are very different in construction scheme and design, and its design vary also from country
to country.
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Wood stoves (residential furnaces, household stoves) are enclosed wood heaters that control
burning or burn time by restricting the amount of air that can be used for combustion.
According to purpose stoves can be classified into: heating, heating-cooking, cookers, bath
furnaces, etc.
Wood stoves are commonly used in residences as space heaters. They are used both as the
primary source of residential heat and to supplement conventional heating systems. Stoves can
be prefabricated and on-site made (mainly masonry).
Noncatalytic wood stoves are those units that do not employ catalysts but that do have emission
reducing technology or features. Typical noncatalytic design includes baffles and secondary
combustion chambers.
Catalytic stoves are equipped with a ceramic or metal honeycomb device, called a combustor or
converter, that is coated with a noble metal such as platinum or palladium. The catalyst material
reduces the ignition temperature of the unburned volatile organic compounds (VOC) and carbon
monoxide (CO) in the exhaust gases, thus augmenting their ignition and combustion at normal
stove operating temperatures. As these components of the gases burn, the temperature inside the
catalyst increases to a point at which the ignition of the gases is essentially self-sustaining.
Pellet stoves are those fueled with pellets of sawdust, wood products, and other biomass
materials pressed into manageable shapes and sizes. These stoves have active air flow systems
and unique grate design to accommodate this type of fuel.
Conventional stoves do not have any emission reduction technology or design features. Stoves
with various airflow designs may be in this category, such as updraft, downdraft, crossdraft, and
S-flow.
Masonry heaters are enclosed chambers made of masonry products or a combination of masonry
products and ceramic materials. Masonry heaters are gaining popularity as a cleaner-burning,
heat-efficient form of primary and supplemental heat, relative to some other types of wood
heaters. In a masonry heater, a complete charge of wood is burned in a relatively short period of
time. The use of masonry materials promotes heat transfer. Thus, radiant heat from the heater
warms the surrounding area for many hours after the fire has burned out.
In the former USSR countries, especially in Russia and Belarus so-called Russian (heating)
stoves are very typical for rural communities. They can be classified as masonry and are mainly
wood stoves but other solid fuels such as peat briqutte are also used (mainly in winter).The main
purpose of russian stove is cooking and household heating (heating-cooking). It is made of brick.
The stove is in the form of an arch and has no wind box and fire grate. The off-take system
includes a shield (located in the front of the oven) collecting flue gases and a smoke stack. The
stoke hole height above the hearth is about 6 m.
Firewood is used as fuel: during the warm season – mainly pinewood, during the cold season – a
combination of pine- and birchwood. I winter wood can be combined with peat briquette. The
stove is usually used daily for 2.5-3 hours.
c. Boilers
Generally boilers are distinguished as steam and hot-water boilers, functioning with natural or
induced (forced) circulation.
Boiler can be identified:
-by fuel type: solid fuel (coal, wood, biomass etc.), liquid, gaseous;
-by the furnace firing configuration (pulverized coal furnace, layer furnace and fluidized bed);
-by the heat transfer method (watertube, firetube);
-by the arrangement of the heat transfer surfaces (horizontal or vertical, straight or bent tube);
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-by the heat (power, steam) capacity;
-by fuel supply (manual-feed, mechanical, semi-mechanical).
c1. Coal combustion
Pulverized-coal boilers
In pulverized coal-fired (PC-fired) boilers, the fuel is pulverized to the consistency of talcum
powder (i.e., at least 70 percent of the particles will pass through a 200-mesh sieve) and
pneumatically injected through the burners into the furnace. Combustion in PC-fired units takes
place almost entirely while the coal is suspended in the furnace volume (in the chamber). PCfired boilers are classified as either dry bottom or wet bottom (also referred to as slag tap
furnaces), depending on whether the ash is removed in a solid or molten state. In dry bottom
furnaces, coals with high fusion temperatures are burned, resulting in dry ash. In wet bottom
furnaces, coals with low fusion temperatures are used, resulting in molten ash or slag.
Depending upon the type and location of the burners and the direction of coal injection into the
furnace, PC-fired boilers can also be classified into two different firing types, including wall and
tangential.
Cyclone furnaces (boilers) are often categorized as PC-fired systems even though the coal is
crushed to a maximum size of about 4-mesh. The coal is fed tangentially, with primary air, into a
horizonal cylindrical furnace. Smaller coal particles are burned in suspension while larger
particles adhere to the molten layer of slag on the combustion chamber wall. Cyclone boilers are
high-temperature, wet-bottom type systems.
Fluidized-bed boillers
In a fluidized bed combustor (FBC), the coal is introduced to a bed of either sorbent or inert
material (usually sand) which is fluidized by an upward flow of air.
Boilers with layer furnaces (stokers) account for the vast majority of coal-fired watertube
boilers for industrial, commercial, and institutional applications.
In layer furnace and most handfed units, the fuel is primarily burned on the bottom of the furnace
or on a grate. The following types of grate are distinguished: stationary grate; moving grate;
sloping grate; traveling grate; dumping grate etc.
Various types of solid fuel including coal, peat briquette and wood are used in layer furnaces.
Watertube boilers. The most common heat transfer method for coal-fired boilers is the watertube
method in which the hot combustion gases contact the outside of the heat transfer tubes, while
the boiler water and steam are contained within the tubes.
Firetube boilers. These boilers are more rare than water-tube and mainly of old design. The most
common types of firetube boilers used with coal are the horizontal return tubular (HRT), Scotch,
vertical, and the firebox. The HRT boilers are generally fired with gas or oil instead of coal. The
boiler and furnace are contained in the same shell in a Scotch or shell boiler. Vertical firetube
boilers are typically small singlepass units in which the firetubes come straight up from the
water-cooled combustion chamber located at the bottom of the unit. A firebox boiler is
constructed with an internal steel-encased, water-jacketed firebox. Firebox firetube boilers are
also referred to as locomotive, short firebox, and compact firebox boilers and employ mechanical
stokers or are hand-fired.
Cast iron and steel boilers are generally shipped in sections and assembled on site. These boilers
commonly used in residences as space heaters. Cast iron boilers are more effective and durable
than steel boilers. These boilers are used to produce either low-pressure steam or hot water, and
are most commonly used in small commercial applications.
Another type of heat transfer configuration used in small boilers is the tubeless design. This
design incorporates nested pressure vessels with water in between the shells. Combustion gases
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are fired into the inner pressure vessel and are then sometimes recirculated outside the second
vessel.
c.2.Biomass Combustion
Various boiler firing configurations are used for burning wood waste. One common type of
boiler used in smaller operations is the Dutch oven. This unit is widely used because it can burn
fuels with very high moisture content. Fuel is fed into the oven through an opening in the top of
a refractory-lined furnace. The fuel accumulates in a cone-shaped pile on a flat or sloping grate.
Combustion is accomplished in two stages: (1) drying and gasification, and (2) combustion of
gaseous products.
In another boiler type, the fuel cell oven, fuel is dropped onto suspended fixed grates and is fired
in a pile. Unlike the Dutch oven, the refractory-lined fuel cell also uses combustion air
preheating and positioning of secondary and tertiary air injection ports to improve boiler
efficiency.
The firing method most commonly employed for wood-fired boilers with a steam generation is
the spreader stoker. In this boiler type, wood enters the furnace through a fuel chute and is
spread either pneumatically or mechanically across the furnace, where small pieces of the fuel
burn while in suspension. Simultaneously, larger pieces of fuel are spread in a thin, even bed on
a stationary or moving grate.
Another boiler type sometimes used for wood combustion is the suspension-fired boiler. This
boiler differs from a spreader stoker in that small-sized fuel (normally less than 2 mm) is blown
into the boiler and combusted by supporting it in air rather than on fixed grates. Rapid changes in
combustion rate and, therefore, steam generation rate are possible because the finely divided fuel
particles burn very quickly.
For the combustion practice of the FSU countries, especially in municipal sectors is typical that
small boilers is fueled by various types of solid fuels (coal, peat, wood, wood wastes etc.)
separately or in a mix without special reequipment.
c.3. Liquid fuel and gas combustion
Boilers for liquid and gaseous fuels are generally close in design and are less diverse than for
solid fuel.
Boilers are classified according to design and orientation of heat transfer surfaces, burner
configuration, and size. The major boiler configurations for oil and gas-fired combustors are
watertube, firetube, cast iron, and tubeless design.
Watertube boilers are used in a variety of applications ranging from supplying large amounts of
process steam to providing space heat for industrial facilities. In a watertube boiler, combustion
heat is transferred to water flowing through tubes which line the furnace walls and boiler passes.
The tube surfaces in the furnace (which houses the burner flame) absorb heat primarily by
radiation from the flames. The tube surfaces in the boiler passes (adjacent to the primary
furnace) absorb heat primarily by convective heat transfer.
Firetube boilers are used primarily for heating systems, industrial process steam generators, and
portable power boilers. In firetube boilers, the hot combustion gases flow through the tubes
while the water being heated circulates outside of the tubes. At high pressures and when
subjected to large variations in steam demand, firetube units are more susceptible to structural
failure than watertube boilers. This is because the high-pressure steam in firetube units is
contained by the boiler walls rather than by multiple small-diameter watertubes, which are
inherently stronger. As a consequence, firetube boilers are typically small and are used primarily
where boiler loads are relatively constant.
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Nearly all firetube boilers are sold as packaged units because of their relatively small size.
Cast iron boilers is one in which combustion gases rise through a vertical heat exchanger and
out through an exhaust duct. Water in the heat exchanger tubes is heated as it moves upward
through the tubes. Cast iron boilers produce low pressure steam or hot water, and generally burn
oil or natural gas. They are used primarily in the residential and commercial (institutonal)
sectors.
Boilers are usually arranged in a boiler unit: system consisting of a boiler, steam heater, water
economizer, air heater, furnace, brickwork, gas ducts, framework, reinforcement and fittings.
Boiler shop where boilers are installed can includes also fuel preparation and supply unit, blow
fan, equipment for residual fuel removal – slag and ash removal, smoke exhauster, and smoke
stack.
3.4
Emissions
A large variety of pollutants are emitted from fuel combustion in small instalations.
Sulphur dioxid emissions depend on SO2 content in fuel; NOx emissions depend on combustion
conditions.
Complete fuel combustion cannot be reached in residential furnaces and small boiler. At
incomplete combustion carbon and its compounds as well as non-metane volatile organic
compounds are emitted together with gases.
Solid particles emitted represent both fly ash and unburnt fuel particles – soot. The ratio of these
components is defined by a fuel type and combustion conditions. Level of its emissions depends
on abatement.
Among heavy metals can be named arsenic, mercury, cadmium, lead, zinc, nickel, cupper,
chromium and selenium from solid fuel combustion. In case of oil combustion also vanadium are
added; from combustion of natural gas only mercury is emitted. Most of the heavy metals are
emitted in aerosol forms; mercury and selenium are presenr in vapour phase. Heavy metal
emissions depend from type of combusted fuel (and HM content in it), type of boiler and
furnaces, processes of burning (temperature of burning, temperature of wastes gases etc).
Dioxin emissions depend on features of fuel (content of volatile organic compounds, moisture,
chlorine) and conditions of combustion.
PAH emissions results on incomplete combustion and depend on type of fuel, temperature in
combustion zone, volatile organic compounds content in fuel, turbulence efficiency of fuel and
air mixing, air and fuel fed volume ratio, etc. Generally from solid fuel combustion more PAH
emitted than from liquid and gaseous combustion.
3.5
Controls
Control techniques for criteria pollutants emission from small combustion may be classified into
three broad categories: fuel treatment/substitution, combustion modification, and postcombustion
control.
Fuel treatment greatly influence POPs emission.
Uncontrolled PM emissions from small stoker-fired and hand-feed combustion sources can be
minimized by employing good combustion practices such as operating within the recommended
load ranges, controlling the rate of load changes, and ensuring steady, uniform fuel feed. Proper
design and operation of the combustion air delivery systems and catalysits application can also
minimize PM emissions.
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The postcombustion control of PM emissions from coal-fired combustion sources can be
accomplished by using one or more or the following particulate control devices:
• Electrostatic precipitator (ESP),
• Fabric filter (or baghouse),
• Wet scrubber,
• Cyclone or multiclone collector, or
• Side stream separator.
In East Europe (FSU) countries medium-size boiler units are equipped in the majority of cases
with simple dust collection units (precipitation chambers, cyclones) with control efficiency from
30 to 60%. Small domestic boilers as well as furnaces of various design are not equipped with
dust collection units.
4.
SIMPLER METHODOLOGY
Simpler methodology is based on using of by-pollutants emission factors connected with
volume of combusted fuel for a certain group of installations:
Ei = Σ EFj*Aj
Ei – annual emission of pollutant i;
EFi – emission factor of pollutant i for the group j (type) of installations;
Aj – volume of combusted fuel by a group of installtion
5.
DETAILED METHODOLOGY
Hardly applicable for this type of sources.
6.
RELEVANT ACTIVITY STATISTICS
Generally statistical data structure on fuel consumption do not show this group of fuel
consumers. Their share can be estimated using additional calculation, for example by extracting
from total fuel consumption the share of energy production where usually large installations are
used.
7.
POINT SOURCE CRITERIA
Not applicable.
8.
EMISSION FACTORS, QUALITY CODES AND REFERENCES
Default emission factors which can be used for estimation of emissions when no other
information can be seen in the table 8.1.-8.3. For their evaluation own data based upon
experience of sources inventory and vast literature data were used (see Bibliography and
References).
Additional information can be find in the Annexes.
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Table 8.1.Default emission factors for solid fuel small combustion installations (boilers)
SNAP CODE
Description:
Pollutant
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
Dioxins and furans
Polycyclic aromatic
hydrocarbons
Benzo(a)pyrene
Benzo(b)fluoranthene
Benzo(k)fluoranthene
Indeno(1,2,3-c,d)pyrene
Coal
Non
Partially
controlled controlled
Emission
Emission
factor
factor
Small and Medium Boilers
Peat
Wood
Non
Partially
Non
Partially
controlled controlled controlled controlled
Emission
Emission
Emission
Emission
factor
factor
factor
factor
0
0.15
0.05
0
0.02
0.07
0.02
0.02
0.02
0.4
0.1
0.06
0.07
0.5
0.1
0.22
0
0
0
0
0.01
0.4
0.1
0.04
0.08
0.5
0.15
0.25
Units
1.0
0.1
1.0
1.4
0.2
1.0
1.5
0.3
0.05
0.3
0.4
0.2
0.3
0.5
5.0
2.5
1.5
1.0
2.0
2.5
0.6
1.0
4.30
5.0
1.30
1.0
g/Mg
g/Mg
g/Mg
g/Mg
g/Mg
g/Mg
g/Mg
g/Mg
g/Mg
g/Mg
ugTEQ/Mg
2.0
3.6
1.4
1.2
0.6
1.08
0.42
0.36
0.8
1.6
0.4
0.4
0.24
0.48
0.12
0.12
5.0
10.3
2.7
2.5
1.5
3.10
0.80
0.75
g/Mg
g/Mg
g/Mg
g/Mg
Table 8.2. Default emission factors for liquid and gaseous fuel small combustion installations
(boilers)
SNAP CODE
Small and Medium Boiler
Description:
Pollutant
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
Dioxins and furans
Polycyclic aromatic hydrocarbons
Benzo(a)pyrene
Benzo(b)fluoranthene
Benzo(k)fluoranthene
Indeno(1,2,3-c,d)pyrene
Belarusian contribution to EMEP
Natural gas
Oil
Emission factor
Units
0.05
0.1
1.0
0.5
0.05
30.0
1.0
g/t oil
g/t oil
g/t oil
g/t oil
g/t oil
g/t oil
g/t oil
1.5
0.2
g/t oil
ugTEQ/Mg oil)
0.0043
0.0086
0.0039
0.0086
g/t oil
g/t oil
g/t oil
g/t oil
15
Emission factor
Units
0.0014
g/m3
0.0015
0.0021
0.0021
0.0012
Annual report 2002
Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
Table 8.3. Default emission factors for small combustion installations (furnaces)
SNAP CODE
Pollutant
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
Dioxins and furans
Polycyclic aromatic hydrocarbons
Benzo(a)pyrene
Benzo(b)fluoranthene
Benzo(k)fluoranthene
Indeno(1,2,3-c,d)pyrene
9
Household furnaces (noncontrolled combustion)
Peat
Wood
Emission
Emission Units
factor
factor
0.06
0
g/Mg fuel
0.03
0.01
g/Mg fuel
0.2
0.03
g/Mg fuel
0.2
0.10
g/Mg fuel
0
0
g/Mg fuel
0.15
0.03
g/Mg fuel
0.24
0.15
g/Mg fuel
g/Mg fuel
g/Mg fuel
1.0
2.5
g/Mg fuel
2.5
5.0
ugTEQ/Mg fuel)
0.8
1.6
0.4
0.4
5.0
10.3
2.7
2.5
g/Mg fuel
g/Mg fuel
g/Mg fuel
g/Mg fuel
SPECIES PROFILES
For this chapter the CEPMEIP data can be used.
10
UNCERTAINTY ESTIMATES
A lot of factors influence uncertainty of emission estimates. They can be divided into a few
groups: connected with emision factors uncertainty, connected with emission factors indequate
applicability, connected with statistical data drawbacks.
To the first group belong drawbacks stipulated by low level of study of this type of sources at all
(in comparison, for instance, with large combustion plants), fuels properties (such as heavy
metals and volatile organics content) variability, installations and operation regime variability.
To the second group belong effects of inhomogenity of this type of sources. Thus suggested
factors resulted from analysis of a certain set of installations, certain types of fuel, in a certain
conditions etc. So country, regional etc. specificity will affect greatly estimated level of
emission.
Last group include all uncertainties connected with imperfection of statistical data, and problems
with extraction or estimation of fuels consumption by installation type.
11
WEAKEST ASPECTS/PRIORITY AREAS FOR IMPROVEMENT IN
CURRENT METHODOLOGY
Priority areas for improvement in simpler methodology: specification of region-specific and bytype of installation emission factors. Further research are necessary on measurements,
investigations of installations for their classification by emission-influencing parameters.
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Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
12
SPATIAL DISAGGREGATION CRITERIA FOR AREA SOURCES
Generally these installations are considered as area sources. Simplest method of emissions
disaggregation – their calculation for administrative units of low level. Country emission can be
also distributed by population density, using special map. Depending on situation separately
urban and rural populations density figures can be used.
13
TEMPORAL DISAGGREGATION CRITERIA
For temporal disaggreagtion data on volumes of fuels used by seasons (month) are necessary.
17
REFERENCES
1. Berdowski J.J.M., Baas J, Bloos JP.J., Visschedijk A.J.H., Zandveld P.Y.J. The European
Atmospheric Emission Inventory for Heavy Metals and Persistent Organic Pollutants.
Umweltforschungsplan des Bundesministers fur Umwelt, Naturschutz und
Reaktorsicherheit. Luftreinhaltung. Forschungbericht 104 02 672/03. TNO, Apeldoorn,
The Netherlands. 1997.
2. Dioxin and Furan Inventories / National and Regional Emissions of PCDD/PCDF.
Geneva: UNEP Chemicals, 1999. 100 p.
3. Emission Factors Manual PARCOM-ATMOS. Emission factors for air pollutants. Final
version -TNO Report 92-233/112322-24285, 1992, 1993.
4. Artjushenko N.M. Heating of Private Houses. Kiev, 1985. 178 p. (in Russian).
5. Compilation of Air Pollutant Emission Factors (AP-42), Volume 1: Stationary Point and
Area Sources, 5th ed., U.S. Environmental Protection Agency, Office of Air Quality
Planning and Standards. Research Triangle Park. North Carolina. 1996.
6. EPA Compilation of Air Pollutant Emission Factors, Section 7.1, Residential Wood
Combustion. 5-th ed: EPA AP-42. United States Environmental Protection Agency.
Research Triangle Park, North Carolina, U.S. 1998.
7. Pacyna J.M., Pacyna E.G. An assessment of global and regional emissions of trace metals
to the atmosphere from anthropogenic sources worldwide. Environ. Rev. 2001, N 9. Pp.
269-298.
18
BIBLIOGRAPHY
Heavy Metals Emission Factors Assessment for the CIS Countries/Kakareka et. al., Minsk. 1998.
160 p.
Karl U., Peter H., Rentz O. Heavy Metal Emissions from Combustion Processes. Determination
and Emission Factors. UN ECE Combustion and Industry Expert Panel Workshop on Emissions
of Heavy Metals and Persistent Organic Pollutants from Large Stationary Sour JRC, Ispra, 4-5
November 2002.
Borsthov D.Ya., Volikov A.N. Environmental protection during small boilers operation.
Moscow, 1987. 153 p. (in Russian).
Sosnin Yu.P., Bukharkin E.N. Heating and hot water-supply of private houses. Moscow, 1991.
384 p. (in Russian).
Reference book on small boiler-houses / Roddatis K.F., Poltaretski A.N. Moscow, 1989. 488 p.
(in Russian).
Belarusian contribution to EMEP
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Annual report 2002
Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
2. DEFAULT EMISSION FACTORS TABLES
According to 2002 Task Force meetings decisions a few default emission factors tables should
be prepared for inclusion into the Guidebook. Non-ferrous industry, large combustion plants,
some ferrous industry sectors were chosen for inclusion as priority.
Draft default chapters were prepared and discussed during Combustion and Industry Expert
Panel meetings in Ispra (April and November 2002) with participation of this report author. Later
the output tables were revised and now their new versions were included into the report with
small description (clarification). For their revision own data based upon experience of sources
inventory and vast literature data were used.
According to the position of the TFEIP default emission tables are proposed for first time
emission calculation and reporting. So the factors proposed should provide a minimal error on
the country level of inventory.
New (revised) values of emission factors are in bold.
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Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
2.1. Primary Lead Production (030304)
Table 2.1. Default emission factors for primary lead production
SNAP CODE
Description:
Pollutant
30304
Primary Lead
Limited control
Emission factor
Abatement
Emission factor
Units
15
50
1
5
g/t Pb
g/t Pb
25
3
5
1
g/t Pb
g/t Pb
1500
200
g/t Pb
150
20
g/t Pb
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
Note
In comparison with version drafted at the Panel Meeting in Ispra (November 2002), we suggest
to change most of emission factors for limited control conditions (except mercury), and arsenic
and cadmium emission factors for better control conditions. All changed values were enlarged –
from 1.8 to 5 times. These improvements are based upon measured data on concentrations of
pollutants in the dust of this production (lead and zinc are dominant, cadmium – subdominat
pollutant) and properties of elements (generally the volatility level). Suggested values for
cadmium and arsenic on our opinion are closer to lowest estimates than to best ones.
So differences between “limited control” and “controlled” are not precisely specified, so some
discrepancies arise when abatement influence upon arsenic emission more greatly than upon
zinc.
Quality rank of emission factors are greatest for lead and zinc (B-C), and lowest – for mercury
(D).
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Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
2.2. Primary Zinc Production
Table 2.2 Default emission factors for primary zinc production
SNAP CODE
30304
Description:
Primary Lead
Limited control
Emission factors
Pollutant
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
Abatement
Emission factors
Units
100
100
250
20
10
10
g/t Zn
g/t Zn
25
6
g/t Zn
g/t Zn
500
50
g/t Zn
7000
700
g/t Zn
Note
Prepared at the Combustion and Industry Expert Panel Meeting default emission factors mainly
based onto our own. In the table (above) we made some improvements for controlled emissions
of arsenic, cadmium and lead so previous ones were out of pattern, when we compare limited
control and controlled emission. In conditions of limited data and uncertainties of differences
between levels of abatement it will be better not to suppose significant and unaccountable
differences on this issue between elements.
Quality rank of emission factors are greatest for lead and zinc (B-C), and lowest – for mercury
(D).
Belarusian contribution to EMEP
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Annual report 2002
Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
2.3. Primary Copper Production (0303006)
Table 2.3 Default emission factors for primary copper production
SNAP CODE
Description:
Pollutant
30304
Primary copper
Limited control
Abatement
Emission factors
Emission factors
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
1000
200
1
4000
0.1
1500
3000
100
7
5000
100
50
0.1
250
0.1
50
200
15
1
300
Units
g/t Cu
g/t Cu
g/t Cu
g/t Cu
g/t Cu
g/t Cu
g/t Cu
g/t Cu
g/t Cu
g/t Cu
Note
This table was prepared at the Combustion and Industry Expert Panel Meeting in Ispra. We
suggest to enlarge values of emission factors for lead and zinc for poorly abated technologies so
made them more close to East European conditions. Content of lead and zinc in copper
production dust is close to copper content or sometimes more due to evaporation of these volatile
metals during smelting process.
Levels of emission factors for improved control conditions when lack of data we should on our
opinion consider comparatively close abatement influence for most of metals.
Quality rank of emission factors are comparatively equal for most of metals (C), and lowest –
for mercury (D).
Belarusian contribution to EMEP
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Annual report 2002
Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
2.4. Grey Iron Foundries (0303003)
Table 2.4 Default emission factors for grey iron foundries
SNAP CODE
Description:
30303
Grey iron foundries
Pollutant
Emission
factor
Units
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
0.3
0.1
1
1
0.04
0.3
3
0.01
1
5
g/t iron
g/t iron
g/t iron
g/t iron
g/t iron
g/t iron
g/t iron
g/t iron
g/t iron
g/t iron
Note
Generally this sector is not a significant source of heavy metals so variation of emission factors
levels not great.
Prepared at the Combustion and Industry Expert Panel Meeting default emission factors table for
this sector on our opinion is acceptable so it incorporate available measurement data including
our own (Kakareka et al, 1998) and inventory activities. But we should change abbreviation LS
onto iron in the units column.
Quality rank of emission factors are comparatively equal for most of metals (C), and lowest –
for mercury (D).
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Additions to the EMEP/CORINAIR Atmospheric Emission Inventory Guidebook
2.5. Coke oven furnaces (010406)
Table 2.5 Default emission factors for coke oven furnaces
SNAP CODE
040201 and 010406
Description:
Coke oven furnaces
Pollutant
Emission factors
Units
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Selenium
Vanadium
Zinc
0.01
0.01
0.15
0.1
0.01
0.1
0.25
-
g/t coke
g/t coke
g/t coke
g/t coke
g/t coke
g/t coke
g/t coke
0.4
g/t coke
Note
Generally this sector is not a significant source of heavy metals emission so variation of emission
factors levels not great.
Prepared at the Combustion and Industry Expert Panel Meeting default emission factors table for
this sector on our opinion is acceptable and close to our estimates (Kakareka et al, 1998).
Quality rank of emission factors are comparatively equal for most of metals (C), and lowest –
for mercury (E).
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Annexes
ANNEXES
1. OBJECTS AND METHODOLOGY OF HEAVY METALS EMISSION TESTING
1.1. Processes and Installations Studied in 2002
In 2002 household and municipal boiler units operating on solid fuel, and also household
furnaces were tested. For the investigation of heavy metals emission from open burning its
simulation with emission sampling and analysis were applied.
Fuel combustion units
This chapter gives a description of boiler units for which ash/soot sampling was conducted.
Boilers used and other equipment are typical for Belarus and other NIS.
Boiler unit of a secondary school. Equipped with hot-water boilers Minsk-1 with a manual fuel
feed. In operation since 1981. No control of exhaust gases. Coal is used as fuel. The kiln
operation is minimized due to the shortage of fuel. The rate of exhaust gases on the horizontal
part of the flue makes up about 2 m/sec.
Boiler unit of a hostel. Equipped with 4 hot-water boilers Minsk-1. Peat briquette and firewood
are used as fuel. Fuel feed is manual. The feed takes place every 15-20 minutes. No control of
exhaust gases. The rate of exhaust gases during experiments is about 8-10 m/sec.
Boiler unit of a secondary school. Equipped with hot-water boilers Universal. Coal is used as
fuel in winter periods, firewood or a fuel mixture (broken peat, coal and sawdust) in other
seasons. Fuel feed is manual. No control of exhaust gases. The fuel load was minimized.
Boiler unit of a district hospital. Equipped with boiler units Е-1/9. Coal is used as fuel in winter
periods, and mainly firewood in other seasons, but often firewood is combusted together with
coal. Fuel feed is manual. A cyclone is used for ash control.
Boiler unit of a secondary school. Equipped with hot-water boilers Minsk-1 and Universal-5.
Coal is used as fuel in winter periods, and mainly firewood in other seasons. Fuel feed is manual.
No control of exhaust gases.
Boiler unit of a secondary school. Equipped with hot-water boilers KVN. There is a device with
a mechanical feed. However, the feed is manual due to the fact, that various types of fuel are
used. The fire-grate often becomes clogged with dust, therefore, the burning is often weak. A
cyclone is used for dust control.
Boiler unit of a kindergarten. Equipped with hot-water boilers Universal-8М. Fuel varies from
coal till peat briquette and firewood. No control.
Boiler unit of a secondary school. Equipped with hot-water boilers KVM-0.8. The fuel is mixed:
in winter coal is mainly used. In spring and autumn peat briquettes and firewood are used. There
is a device for coal mechanical feed on the fore part of the boilers. Peat briquettes and firewood
are fed into the furnace from the backside. The stoke slat is out of order. The boilers become
heavily clogged with soot and ash and their cleaning is needed annually. A cyclone is used for
dust control.
Russian stove. The main purpose is cooking and winter household heating. It is made of brick.
The stove is in the form of an arch and has no wind box and fire grate. The off-take system
includes a shield (located in the front of the oven) collecting flue gases and a smoke stack. The
stoke hole height above the hearth is about 6 m. Gas rate in the stoke hole makes up 1-2 m/s.
Off-gases in the stoke hole are maintained at a temperature of 120оС.
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Annexes
Firewood is used as fuel: during the warm season – mainly pinewood, during the cold season – a
combination of pine- and birchwood. The oven is used daily for 2.5-3 hours. The amount of
firewood combusted is about 10 kg/day.
Kitchen range. The main purpose is cooking fodder for domestic animals. The range is made of
brick. The combustion chamber is a rectangular and overlapped with pig iron plating from above
in the form of a double-burner stove with seams. The range is equipped with a fire grate and a
wind box door for free access for air. The chimney is located in the back of the range. The
chimney’s height is 2.15 m.
Wood waste (mainly board and cants ends, old lamp posts, etc.) and firewood are used as fuel.
The stove is operated daily during 2-2.5 hours. The amount of firewood combusted is about 5-7
kg/day.
The off-gas temperature ranges within 70-340оС and depends on the amount of the materials
combusted and the combustion rate.
Main parameters of objects study and types of collected samples are given in Table 1.
Table 1. Main parameters of tested installation
Combustion unit, control
Kitchen range, no control
Russian stove, no control
Small boiler, no control
Small boiler, no control
Boiler E/9, cyclone
Boiler Minsk-1, no control
Boiler Minsk-1, no control
Boiler Minsk-1, no control
Boiler KVN, cyclone
Fuel
Wood, wood waste
Wood
Peat briquette
Coal
Coal, wood
Coal
Peat briquette, wood
Wood
Coal, peat briquette
Boiler Universal, no control
Boiler Universal, no control
Peat briquette, wood
Coal, peat briquette,
sawdust
Type of collected samples
Fly ash
Fly ash, soot from walls of chimney
Fly ash, soot from walls of chimney
Residual ash, soot from walls of chimney
Residual ash, soot from walls of chimney, fly ash
Residual ash, soot from walls of chimney, fly ash
Residual ash, soot from walls of chimney, fly ash
Residual ash, soot from walls of chimney, fly ash
Residual ash, soot from walls of chimney and from
cyclone, fly ash
Soot from walls of chimney, fly ash
Residual ash, soot from walls of chimney, fly ash
Open burning
We have tested 4 types of open burning processes: forest fires, peatland fires, agricultural wastes
burning and domestic wastes burning.
Among real burning cases we controlled the following: peatland fires, forest fires, household
waste and leaves fall-off open burring. The samples of ash from bonfire were collected.
A special unit was constructed for model combustion: combustion was done in an open metal
box (dimensions 50x40x20 cm) with the holes on the lower side, and with legs with height 20
cm. Combustion was performed in conditions similar to the real open combustion of wastes.
During testing the cases of fires combusted material volumes, its composition, combustion rate
and condition of burning were measured.
Forest fires. We have used forest bed leaves collected in the pine wood to simulate back forest
fire. The bed morphological composition was formed in such a way so that there were variants
with woods (bows) and ground soil elements represented by humus and vegetation residue.
Peatland fires. Peat collected at the worked-out high bog and dried mixed peat as well as peat
from the wild section of the high bog near Minsk were used to imitate peatland fires. A small
amount of wood was used as a substrate burnt also.
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Annexes
Agricultural waste burning. Combustion was performed in smouldering conditions. Potato haulm
formed substrate composition. Tomato haulm, strawberry leaves, French beans stalks, straw were
also used as admixture.
Household waste burning. Samples with different ratio of paper, package material, wood and
other components most often incinerated both in refuse containers and on fire (typical for private
residential areas) were used for simulation of household wastes open burning.
1.2. Methodology of Emission Sources Testing
Experimental work for the HM emission factors evaluation included:
• aerosol and vapour HM sampling from off-gases;
• fly ash sampling from stack walls and from control equipment;
• ash sampling (from bonfires and ashpits);
• fuel sampling;
• samples preparations;
• analytical determination of HM in samples;
• data processing.
Experimental work has been carried out according to the current regulations in the CIS countries
(Manual on control of air pollution sources, 1992; Methods of determination of gas-dust flow
rates from stationary sources of pollution; Procedures of measurement of pollutant
concentrations in emissions of enterprises of building materials industry, 1989; Manual on air
pollution control, 1991 etc.). Since the control of HM emission gas component is not yet
regulated by the normative-methodological documents of the CIS countries, the corresponding
methodological elaborations of the US Environmental Protection Agency (methods 5 and 29
EMTIC) have been used during sampling.
Off-gases sampling from fuel combustion unit
The aerosol and vapour phases of HM were collected by ordinary sampling train with pumping
of waste gases through the filter (first stage) and sorbent (second stage). Sampling equipment
included a dust collection probe, filter holder and filter, sorbent module, electric aspirator with
rotameter, thermometer, anemometer.
As filter for aerosol phase of HM synthetic fibre filters were used. For the collection of vapour
phase of HM the liquid sorbent (mixture of 5% HNO3 and 10% peroxide hydrogene) were used.
Sampling from boiler was performed in horizontal part of stack, from household furnaces – at
the outlet.
Off-gases sampling from open burning
The aerosol and vapour phases of HM were collected by ordinary sampling train with pumping
of waste gases through the filter (first stage) and sorbent (second stage).
Sampling equipment included a nozzle with filter holder and filter, dust collection probe, sorbent
module, electric aspirator with rotameter, thermometer, barometer, psychrometer, anemometer.
As filter for aerosol phase HM glass wool were used. For the collection of vapour phase HM the
liquid sorbent (mixture of 5% HNO3 and 10% peroxide hydrogene) were used. Sampling of flue
gases was done at temperatures of 15-100оC. Filters were located 10-30 cm from the source of
open burning taking into account the wind direction. Sampling was done for 60 min with an
average sampling rate of 10 l/min.
Sampling procedures and samples preparation were agreeable to the standards on the filter
materials technical characteristics. Sampling unit leak-proofness, chemical vessels preparations
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for liquid samples storage and handling were done. Before sampling filters were placed in
desiccator, brought to permanent weights and weighed. Before and after each sampling the
sampling units (tubes, hoses, vessels, fridge) were rinsed.
The experimental works involved, apart from the flue gas sampling, the study of main fuels
properties (moisture, ash content, composition) and their combustion conditions, evaluation of
burnt organic matter mass and its composition, and also off-gas main parameters.
After sampling solid samples were packed in preliminary prepared calque envelopes, then each
sample was placed into a plastic bag. Before the analysis samples were kept in the fridge.
1.3. Heavy Metals Analytical Determination
The determination of heavy metal content (Zn, Cu, Cd, Ni, Pb) in samples was carried out on the
spectrometer Perkin Elmer AAC 5100 PC\ZL - one of the most up-to-date in Belarus. Detection
limit without concentration - 10-8 – 10-11 for flame ionization and graphite furnace accordingly.
Detection error – within the limit ± 20%.
Metals from solid samples are extracted by their acid digestion in concentrated nitric acid «Fisher trace metal grade».
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Annexes
2. RESULTS OF HEAVY METAL EMISSIONS TESTING
2.1. Solid Fuels Combustion in Small Installations Testing
Heavy metals content in fly ash
Firewood combustion
HM emissions for firewood combustion were studied on the example of two types of household
furnaces (Russian oven and kitchen-range) and also a boiler Minsk-1. Various types of firewood
and polluted wood were used as fuel.
Firewood ash content in firewood was low: from 0.24 to 2.4%; on the average, a value of 0.6%
was used for calculations. As expected, ash was enriched with HM during firewood combustion.
Here, HM content in residual ash (from ash pit) and in ash deposited on stack walls was almost
identical and was equal to the HM content in wood recalculated to ash. In some cases ash
deposited on flue stacks has lower HM content values, that can be explained by a significant ash
pollution at the primary stages of firewood combustion (Figures 2.1, 2.2).
800
700
mg/kg
600
500
400
300
200
100
0
Cd
Cr
Cu
Ash from ashpit
Ni
Pb
Zn
Fly ash and soot from chimney walls
Figure 2.1. HM content in differ types of ash from wood combustion in household furnaces
900
800
700
mg/kg
600
500
400
300
200
100
0
Cd
Cr
Ash from ashpit
Cu
Ni
Pb
Zn
Fly ash and soot from chimney walls
Figure 2.2. HM content in differ types of ash from wood combustion in boiler “Minsk-1”
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Fly ash has high concentrations of cadmium, zinc, lead and, to a lesser extent – copper and
nickel. For example, cadmium content in fly ash is sometimes 10 times higher, zinc - 2-5 times
exceeds the content in ash deposited on flue stacks. The explanation of it can be a fine
composition of the emitted ash that is rather typical of various fuel combustion. Among other
factors that influence HM high content in emissions from firewood combustion is a widely used
incineration of some wastes (practically all types of polluted wood, paper, packing material, rags,
etc.). In particular, we have stated maximum zinc in fly ash for chipboard combustion in a
household furnace.
HM rise in fly ash is also possible for wood waste combustion with a large bark content and also
for combustion of firewood harvested in urban territories. In particular, significant differences in
zinc content for fly ash are probably connected with initial concentrations of this metal in the
fuel for fir-tree and poplar separate combustion in the boiler Minsk-1 (Figure 2.3): 2.3 and 53.6
mg/kg respectively.
3000
2500
mg/kg
2000
1500
1000
500
0
Cd
Cr
Cu
Ni
fir
Pb
Zn
poplar
Figure 2.3. HM content in fly ash (collected by filter) from wood combustion in boiler “Minsk-1”
Peat briquette combustion
The analysis of HM content in emission from peat briquette combustion was made on the basis
of previous investigations data for typical fuel-combustion units (Kakareka et al, 1998).
The experimental data showed the wide range of HM content in fly ash for peat combustion: for
example, for zinc – 124-9800 mg/kg, cadmium – 2.4-50, lead – 38- 858 mg/kg. Actually, the
upper limit of values coincides with the data for coal combustion. It can be stipulated by the fact,
that fine ash of coal previously combusted in the same boiler, is drawn into gas stream (as, for
example, in the boiler KVN of a boiler unit in Zasovje secondary school).
According to the data obtained, peat ash is concentrated with HM in comparison with the initial
fuel. Zinc exceeds in absolute values among the elements under study (Figure 2.4).
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250
mg/kg
200
150
100
50
0
Cd
Cr
Peat briquette
Cu
Ni
Ash from cyclone
Pb
Zn
Fly ash collected by filter
Figure 2.4. Comparison of HM content in peat briquette and in differ types of ash from it
combustion in boiler DKVR
We detected close values of HM content for firewood and peat combustion in ash and soot
deposited on flue stacks. One can notice differences only for zinc: firewood ash has zinc almost
twice as much (Figure 2.5).
600
500
mg/kg
400
300
200
100
0
Cd
Cr
Cu
peat ash
Ni
Pb
Zn
wood ash
Figure 2.5. HM content in fly ash (accumulated on the wall stack) from peat briquette and wood
combustion
Coal combustion
We studied emissions from coal combustion for two boiler types: Minsk-1 and KVN. The data
obtained show a rather identical ash composition both in ash pit and in that deposited on flue
stacks, and that collected by the cyclone. For example, chromium content ranges from 30 to 40
mg/kg, copper– 20-88, nickel – 6-10, lead – 10-20, zinc – 305-486 mg/kg. The exception is
cadmium, its content is rather high in ash emitted by gas stream and deposited during its
streaming.
Aerosol particles collected by the filter from the flue gas stream were enriched with HM in
comparison with residual ash and initial fuel: surcharges make up 10-20 times and more.
Especially fly ash is enriched with cadmium, lead and zinc, although less fly elements (nickel
and copper) have also high concentrations (Figure 2.6). According to (Karl et al., 2002),
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volatility of copper, nickel, chromium and some other metals can increase under certain
conditions, and here fine fractions are enriched.
500
450
400
mg/kg
350
300
250
200
150
100
50
0
Cd
Cr
Ash from cyclone
Cu
Fly ash from wall stack
Ni
Pb
Fly ash collected by filter
Figure 2.6. HM content in differ types of ash from coal combustion in boiler KVN (Zasovje, Logojsk
region)
Some other editions show HM content high variability in emissions for coal combustion (Jockel,
Hartje, 1995). Here, zinc content in fly ash after exhaust gas control can make up 7 g/kg, lead –
5, arsenic – 1.3 g/kg.
Combustion of mixed fuels
Boiler units and household furnaces during the heating period are fueled usually by various solid
fuels or solid fuel mix. For instance, simultaneous feed by coal and firewood, firewood and peat
bricks, coal and peat bricks (together with sawdust and other wood wastes), etc. is possible. We
have conducted sampling from mixed solid fuels combustion in boilers Е/9, Universal and
Minsk-1.
One should point to the fact, that HM concentration variation in the collected ash like are typical,
although the range is not large in the majority of cases (Figure 2.7).
It was stated, that close-range HM contents are found in fly ash during fuels co-combustion, i.e.
levels smoothing takes place. At the same time, high concentrations of the majority of metals are
traced if coal is present or there is its high content in fuel composition. Fly ash of coal is rather
concentrated with zinc; yet, during co-combustion of fuels zinc content in fly ash is several times
lower (Figure 2.8).
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700
600
mg/kg
500
400
300
200
100
0
Cd
Cr
Peat+wood
Cu
Coal+wood
Coal+peat+sawdust
Ni
Coal
Pb
Peat
Wood
Figure 2.7. HM content in fly ash collected by filter from solid fuel combustion
12000
10000
mg/kg
8000
6000
4000
2000
0
Peat+wood
Coal+peat+sawdust
Coal+wood
Coal
Peat
Wood
Figure 2.8. Zinc content in fly ash collected by filter from solid fuel combustion
The leveling of various emissions for fuel co-combustion can be seen in the study results of ash
and soot collected from flue stacks (Figure 2.9). Deposited ash and soot show mean composition
of the stream of suspended substances formed during fuels combustion while accumulating
during one or more heating periods.
We failed to detect dependences of HM content in fly ash according to the type of a fuel
combustion unit, since the boilers studied (Minsk-1, Universal, Е, КVN) make up one group of
furnaces: they are all fuel-bed type with a stationary grid.
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600
500
mg/kg
400
300
200
100
0
Cd
Cr
Cu
Peat+wood
Coal+peat
Ni
Pb
Coal+wood
Wood
Zn
Coal
Figure 2.9. HM content in fly ash and soot from solid fuel combustion (collected from wall stack)
The data received for fly ash properties are shown in the Table 2.1. Soot content ranges from 10
to 35%.
Table 2.1. The main parameters of fly ash and soot, accumulated on the wall
stack
Type of fuel
Coal
Coal+wood
Coal+peat+wood
Peat+wood
Coal+peat
Wood
Moisture content, %
1.0-11.0
0.8-3.9
1.3-4.4
1.1-29.2
4.2-5.6
2.7
Ash content, %
69.2-92.5
65.1-84.8
78.1-83.6
46.1-67.8
47.3-78.8
56.3
Heavy metals content in exhaust gases
Boilers
HM concentrations in exhaust gases from solid fuels combustion in boilers are far from being
defined precisely (Figure 2.10). For example, differences in the content of cadmium, copper and
lead make up 12 times, chromium and zinc 7-8 times.
The data presented show a significant exceed of permissible concentrations limits for these
elements in the atmospheric air.
The study results revealed absence of direct dependence between HM content in fly ash and their
concentrations in exhaust gases. For example, a maximum concentration of most HM is typical
of exhaust gases for a boiler unit in hospital (boilers Е9/1, cyclone as a dust control equipment),
for co-combustion coal and firewood, when the highest HM contents in fly ash were traced for
coal combustion.
Household furnaces
Measured HM concentration in exhaust gases from firewood and wood waste combustion in
household furnaces ranged from 0.85 to 3.6 µg/m3 for cadmium, from 7.8 to 38 for lead and
from 93 to 2183 µg/m3 for zinc. Maximum HM values exceed such for boilers, that can be
explained by the fact, that polluted fuel is used in household furnaces, and that probably HM are
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polluted (accumulated) in ash and soot in gas conduits and then are partially removed during
combustion.
30
25
mkg/m
3
20
15
10
5
0
Cd
Cr
Peat+wood
Cu
Coal+peat+sawdust
Ni
Coal+wood
Coal
Pb
Wood
Peat
Figure 2.10. HM content in waste gases from solid fuel combustion, mkg/m3
Maximum zinc concentration was detected in exhaust gases for firewood and peat briquette cocombustion (Figure 2.11).
300
250
mkg/m3
200
150
100
50
0
Peat+wood
Coal+peat+sawdust
Coal+wood
Coal
Wood
Peat
Figure 2.11. Zinc content in waste gases from solid fuel combustion, mkg/m3
Probably, HM concentration in exhaust gases is defined apart from fuel composition and
properties, by a combustion mode and off-gases control efficiency. Since HM concentration in
off-gases is closely connected with their dust content, then combustion modes, forced ventilation
use for air feed into the furnace, gas conduits systems, etc. will be among determining factors.
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2.2. Heavy Metals Content in Emissions from Open Burning Processes
This category of emission sources covers various types of burning both natural and
anthropogenic: forest fires, grassland and peatland fires, dump fires, household fires, transport
fires, etc. This source category can contribute to a some extent in HM emissions. It is stipulated
both by the diversity of a substrate exposed to burn and by the specificity of burning conditions.
At the same time, data on HM emissions are rather scarce. Due to this, we made experimental
studies of emissions for open burning, including modeling of open burning processes and ash
sampling on fire sites and camp-fires. A modeling was made for litter, peat, agricultural debris
and domestic wastes burning. We studied also ash composition from camp-fires after fall-out and
domestic waste burning, and after grass and peat burn-out.
As it is known, part of HM from the initial material emitted with soot and ash to the air during
burning. The mass of metals emitted to the air depends on a number of factors: type and
composition of a substrate burning, its moisture content, mode of burning, etc. One can
marginally define HM emissions during burning by ash residue composition. As Table 2.2
shows, all types of open burning concerned are emissions sources of copper, nickel, lead and
zinc.
Table 2.2. Mean content of HM in residual ash from open burning, mg/kg
Source (number of samples)
Peat fire (3)
Municipal and domestic wastes
burning (4)
Leaves fall-off burning (4)
Grassland burning (3)
Cd
0.08
0.04
Cr
12.8
63.79
Cu
10.52
133.71
Ni
11.68
18.79
Pb
9.59
870.31
Zn
41.7
33543.2
0.39
0.01
11.84
0.24
46.02
56.29
10.24
6.82
69.51
26.00
453.0
1813.2
Chromium emissions probably take place only during waste burning. Cadmium content is not
high in ash, that can be explained with the element volatility and its emission into the air together
with fine aerosols and gas-vapor constituent. Zinc has a large residue in ash among all HM
concerned. It is connected, on the one hand, with the element high bioaccumulativity, and, on the
other hand, with its wide use, and, as a result, its high content in waste.
HM content in fly ash collected by the filters during modeling of burning processes is shown on
the Figure 2.12.
400
350
300
mg/kg
250
200
150
100
50
0
Cd
Cr
Litter
Cu
Peat
Ni
Pb
Zn
Agricultural debris
Figure 2.12. HM content in fly ash from model combustion of litter, peat and agricultural debris, mg/kg
Belarusian contribution to EMEP
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The highest HM emission concentrations take place during waste burning, and the lowest during
peatbed fires and vegetation burn-out of all types of open burning under study.
Cadmium concentration in fly ash for litter, peat and agricultural debris burning is practically the
same. A marginal concentration range is characteristic of copper and lead. Contrary to this,
chromium, nickel and zinc concentrations for the substrates burning concerned differ greatly - 5
times and more. HM concentration is rather prominent in fly ash for domestic waste burning,
where HM content 1–2 times higher than in fly ash for other substrates burning.
Comparisons of HM concentrations in fly ash collected during experimental peat burning with
HM concentration in ash from seats of fire show high HM concentrations of fly ash: with copper,
cadmium and nickel – more than 5 times, zinc and chromium – 1.5–2.5 times. Lead
concentrations in fly ash and peat ash residue differ slightly.
Fly ash formed during solid domestic waste burning has high cadmium, copper and nickel
concentrations in comparison with ash residue (166, 30 and 8 times respectively). Chromium,
lead and zinc concentrations in fly ash and ash residue were practically the same. The highest
HM concentrations in exhaust gases are formed during domestic waste burning (Figure 2.13).
HM concentrations are considerably lower for exhaust gases formed during litter, peat and
agricultural debris burning, nevertheless, they are several times higher for lead, nickel and
copper than the permissible concentration limits for populated areas (Figure 2.14).
500
450
400
300
mkg/m
3
350
250
200
150
100
50
0
Cd
Cr
Cu
Ni
Pb
Zn
Figure 2.13. HM concentration in waste gases from open burning of domestic wastes, mkg/m3
30
25
mkg/m3
20
15
10
5
0
Cd
Cr
Litter
Cu
Peat
Ni
Pb
Zn
Agricultural debris
Figure 2.14. HM concentration in waste gases from open burning of litter, peat and agricultural debris,
mkg/m3
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3. MATERIALS TO THE EMEP/CORINAIR ATMOSPHERIC EMISSION
INVENTORY GUIDEBOOK REGARDING HEAVY METALS EMISSION
3. 1 Solid Fuel for Small Combustion Description
Boiler units operate both on solid fuel (coal, peat, firewood, wood waste), and on liquid and
gaseous fuel. In furnaces only solid fuels are used. Firewood and peat are most often used as
fuels in the countryside and sometimes in the city private sector. Coal and natural gas are
combusted also in small residential boilers.
Boiler units often are fueled by mixed solid fuel depending on a season.
Ash and moisture content
Ash and moisture belong to the main parameters of solid fuel. Thus, high ash content in coal or
peat stipulates for large amount of particulate matter emissions. In the Table 3.1 moisture and
ash content in solid fuel combusted in typical boilers and furnaces in Belarus are given. One can
notice high moisture content in firewood – up to 44.3%, and also high ash content for coals:
typical values range from 24 to 36%.
Table 3.1. Measured moisture and ash content in solid fuel
Fuel
Peat briquette
Wood, waste wood
Coal
Moisture content, %
12.6-18.9
9.8-44.7
2.6-15.6
Ash content, %
11.2-25.2
0.24-2.8
8.2-36.3
Heavy metal content
Coal
Level of heavy metals content in coal is one of the most important reasons of the certain levels
HM emission from its combustion. The information available on HM content in fuel is rather
heterogeneous. It depends on country, coal basin, open-casts, mine etc; compilation of results
can be seen in the Table 3.2.
Table 3.2. Heavy metals content in coal, mg/kg
Region, sources of data
As
Cd
CIS (on data of Yusfin et al,
15-25
1998)
USSR (on data of Yudovich et
25
0.3
al, 1985; Kler et al., 1987;
Shpirt et al., 1990)
East Ukraine (Manual on
23.5
Heavy Metals…, 2001)
(5-50)
Russia (Coal Quality…, 2001)
16.9
0.38
Europe (Karl et. al., 2002)
1.46-63.4 0.01-0.56
Germany (Karl et. al., 2002)
4-14.5
0.3-1.9
USA (USGS. Coal Quality…,
24.3
0.41
1994 (>7000)
(0-2200) (0-160)
Experimental data (mainly
0.25
Russian coal)
Cr
1-20
Cu
10-90
Hg
-
Ni
2-40
Pb
25-30
18
10
0.05
10
15
Se
up to 5
V
8-35
Zn
20-25
35
53.7
27.6
0.42
28.4
16.2 (5.3(10-160) (15-60) (0.02-2.9)
(10-58)
66)
25.0
18.4
0.17
14.8
9.4
6.4-260 0.28-43.5 0.025-1
9.0-50.7 0.3-5.05
10-26.5
19-33
0.2-0.4
25-45
14-68 nd-2.3
13.9
16.1
0.18
14.7 (0-280)
10.5
2.82 (0(0-200) (0-280)
(0-63)
(0-1900)
150)
8.24
9.29
9.2
7.11
-
-
41.2
(14-109)
48.9
20-121 4.5-405
30-75
35-90
21.6
58.9
(0-330) (0-51000)
36.2
Peat briquette
HM content in peat briquette depends on peat type and its main characteristics (first of all, ash
content) and, sometimes, its pollution degree. We didn’t find the data regarding HM content in
peat briquette; only data for peat was found.
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According to our experimental data, HM content in peat briquette is rather low and is
comparable to its content in wood for most elements (Table 3.3).
Table 3.3. Mean content of HM in peat and peat briquette, mg/kg dry matter
Region, sources
USSR (Shpirt et al., 1990)
Belarus (Kukharchyk, 1996)
Belarus (by experimental work)
Cd
0.05-0.42
Cr
7.0
2.79
1.4-6.7
Cu
7.0
5.20
0.9-9.4
Ni
5.0
2.21
0.4-9.4
Pb
1.8
3.52
1.2-33.7
Zn
16.0
17.5
6.0-27.1
Firewood
Firewood is one of the less studied types of fuel regarding heavy metals content. Bark, needles,
leaves and last-year sprouts were studied in a more detail in order to define HM content. Their
content in wood is defined rather rarely.
We detected HM content in the wood of various tree species used as a local fuel (Table 3.4).
Table 3.4. HM content in wood and tree bark, mg/kg dry matter
Species (number of samples)
Cd
Cr
Cu
The results of experimental work
Fir wood (2)
0.06
0.22
0.84
Poplar wood (1)
0.03
0.01
1.71
Asp wood (1)
0.06
0.01
0.72
Pine wood (3)
0.06
0.42
0.59
Literature data
Pine wood (Kakareka, 1996)
0.04-0.05 0.18-0.24 2.6-3.3
Pine bark – background (Ecogeochemistry,
0.1
1.0
6.0
1995)
Pine bark in impact zones (Ecogeochemstry, 0.32-0.48
6.0
16-20
1995)
Bark of pine, fir and lime near plant of lead
4.0-10
crystal glass (Khomich et al., 2001)
Ni
Pb
Zn
0.4
0.05
0.75
0.73
0.3
0.56
0.15
0.2
4.89
53.62
9.0
3.66
1.1-1.5
-
0.44-0.57
2.0
8.1-23.6
13.0
-
20-25
60-990
1.1-2.5
85-150
40-150
Residual oil
The data on HM content in residual oil are rather scarce. According to the data (Judovich et al.,
1985), nickel content in Russian residual oils ranges from less than 0.4 to 124 mg/kg for the
mean content 47 mg/kg, lead – form the values below the method sensitivity limit up to 3.4
mg/kg (mean value 1.3 mg/kg). Mean zinc content makes up 1.7 mg/kg, copper – 0.38. There are
no data available on cadmium content in Russian residual oils. Its mean content in crude oil is
assumed to make up 0.02 mg/kg (Savenko, 1991).
We did not find data on mercury content for residual oils combustion in the CIS countries. There
are scarce data available on mercury content in crude oils. Thus, V.V.Ivanov (1997) shows data
on mercury content in oils from various deposits all over the world ranging from 0.02 to 30
mg/kg, mean value is assumed to be 7.2 mg/kg. Close to this estimate is mercury content in oils
from Mangyshlak deposits - 6 mg/kg, however, these are the only data available on oils in the
CIS used to calculate mean values. N.A.Ozerova (1986) gives data on mercury content in oils
from Borislavsk deposit (Ukraine) - 1 mg/kg. On the whole, the data are rather limited and the
range of values is too great to obtain reliable mean values.
As the analysis shows, the problem of mercury emissions estimation for residual oil combustion
has not been solved for many European countries: the emissions are evaluated only in some of
them (Berdowski et al., 1997). Mercury content has not been thoroughly studied in oils and
residual oils used in the USA. According to the generalization (Locating and Estimating..., 1993)
mean mercury content in residual oils makes up 0.056 mg/kg, in crude oils - 3.5 mg/kg.
Belarusian contribution to EMEP
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Natural gas
Of all heavy metals considered only mercury might be contained in significant amounts in
natural gas, and the range of its concentrations varies within rather wide limits. Thus, according
to the data (Gritsenko et al., 1993) the content of mercury in natural gas, that goes to the
Astrakhan Gas Processing Plant is 0.3-2.5 µg/m3. Therefore, for calculations it is possible to take
averaged values 1.4 µg/m3, which are consistent with European data, that are in the range 2-5
µg/m3.
3.2. Compilation of Heavy Metal Emission Factors for Small Combustion
HM emission factors by different types of small combustion installation are very poorly
elaborated. Usually measurements are conducted for specific installation and fuels so this data
can hardly been used for another types. So generally aggregated data is used disregarding
specificity of installations and fuels. Tables below (3.5-3.8) shows data available on the issue.
Table 3.5. HM emission factors for oil combustion, g/t
Source
All combustion (Pacyna J. and
Pacyna, 2001)
Small combustion (Berdowski
et al., 1997)
Distillate fuel oil (Compilation
of Air…, 1996)
№6 fuel oil (Compilation of
Air…, 1996 )
Emission Factors Manual…,
1993
Small and medium boilers –
non controlled (authors
estimates)
As
0.02
Cd
0.05
Cr
1.0
Cu
0.5
Hg
0.06
Ni
20.0
Pb
2.0
Zn
1.0
1.0
0.30
2.5
0.55
-
35.0
1.0
1.0
0.07
0.19
1.0
-
0.05
0.31
0.16
-
0.15
0.04
0.01
0.20
0.01
9.6
0.17
3.32
0.6
0.5
1.4
0.5
0.15
30
1.1
0.6
0.02
0.05
0.48
0.36
0.05
44.0
1.26
1.62
Table 3.6. HM emission factors for coal combustion, g/t
Source
All combustion (Pacyna J. and
Pacyna, 2001)
Small combustion (Berdowski
et al., 1997)
High level of abatement
(Compilation of Air…, 1996)
Domestic furnaces
(Determination of Mean…,
1996)
Small consumers
(Determination of Mean…,
1996)
Small and medium boilers – non
controlled (authors estimates)
Small and medium boilers –
limited control (authors
estimates)
Belarusian contribution to EMEP
As
0.2
Cd
0.10
Cr
1.7
Cu
1.4
Hg
0.5
Ni
2.0
Pb
1.0
Zn
1.5
0.25
0.10
0.70
1.0
0.22
1.25
5.00
10.0
0.20
0.03
0.13
-
0.04
0.14
0.21
-
0.16
0.16
-
-
-
-
6.60
-
0.19
0.10
0.06
0.08
-
-
5.70
0.30
3
0.04
1.24
1.4
0.2
0.52
1.3
5.4
0.9
0.01
0.37
0.42
0.2
0.15
0.4
1.62
40
Annual report 2002
Annexes
Table 3.7. HM emission factors for peat combustion, g/t
Source
Industrial combustion
(Berdowski et al., 1997)
Small combustion (Berdowski
et al., 1997)
Small and medium boilers –
non controlled (authors
estimates)
Small and medium boilers –
limited control (authors
estimates)
Household furnaces - non
controlled (authors estimates)
As
0.04
Cd
0.10
Cr
0.03
Cu
0.20
Hg
0.06
Ni
0.03
Pb
0.20
Zn
0.05
0.04
0.04
0.17
0.24
0.06
0.17
0.24
0.05
0.13
0.07
0.38
0.45
-
0.36
0.52
2.0
0.04
0.02
0.11
0.14
-
0.10
0.15
0.6
0.06
0.03
0.17
0.21
-
0.15
0.24
0.9
Table 3.8. HM emission factor for wood combustion, g/t
Source
Industrial combustion
(Berdowski et al., 1997)
Small combustion (Berdowski
et al., 1997)
Traditional domestic wood
furnace (Compilation of Air…,
1996)
Domestic furnace
(Determination of Mean…,
1996)
Small consumers
(Determination of Mean…,
1996)
Wood combustion (Emission
Factors Manual…, 1993)
Small and medium boilers – non
control (authors estimates)
Small and medium boilers –
limited controlled (authors
estimates)
Household furnaces - non
controlled (authors estimates)
Belarusian contribution to EMEP
As
-
Cd
0.10
Cr
0.03
Cu
0.20
Hg
0.10
Ni
0.03
Pb
0.20
Zn
2.0
-
0.04
0.17
0.24
0.10
0.03
0.24
2.0
-
0.011
<0.0005
-
-
0.007
-
-
0.003
0.03
0.09
0.16
-
0.017
0.19
4.2
0.03
0.04
0.21
0.28
-
0.014
1.34
6.85
-
<0.1
-
<0.1
0-0.2
-
<0.05
2.0
0
0.02
0.06
0.22
0
0.04
0.25
4.30
0
0.02
0.02
0.07
0
0.01
0.08
1.30
0
0.01
0.03
0.12
0
0.03
0.15
2.5
41
Annual report 2002
References
REFERENCES
1. Atmospheric Emission Inventory Guidebook. A joint EMEP /CORINAIR Production
Prepared by the EMEP Task Force on Emission Inventories, 1996 (2nd edition - 1999; 3d
edition - 2001).
2. Berdowski J.J.M., Baas J, Bloos JP.J., Visschedijk A.J.H., Zandveld P.Y.J. The European
Atmospheric Emission Inventory for Heavy Metals and Persistent Organic Pollutants.
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