Archived: Air Pollutant Emission Inventory report: annex 2

Asphalt Paving Industry consists of emissions released during asphalt concrete (or hot-mix asphalt) manufacturing. Asphalt concrete manufacturing includes the heating and mixing of asphaltic cement with a mixture of graded aggregates. The sector applies to both permanent or portable hot-mix asphalt installations.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Total usage of asphalt by province/territory is multiplied by pollutant-specific emission factors.

Cutback and emulsion asphalt data to calculate VOC emissions from paving process: SNC/GECO Canada (1981)

Asphalt usage data from construction sector: Statistics Canada (2015c)

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p: Senes Consultants (2008)

VOCs from paving: SNC/GECO Canada (1981)

Concrete Batching and Products include emissions produced by activities at concrete batching plants.

Concrete is composed essentially of water, cement, fine aggregate (i.e. sand) and coarse aggregate (i.e. gravel, crushed stone or iron blast furnace slag). Concrete batching plants store, convey, measure and discharge these constituents into trucks for transport to a construction site or process, for use in the manufacturing of concrete pipe, concrete blocks, etc.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, Pb, Cd

Total usage of cement by province/territory (using national data with a provincial/territory population distribution), is multiplied by pollutant-specific emission factors.

Cement consumption distribution for the provinces: CANMET (1993)

Cement production data: NRCan (2015)

Population data for the provinces: Statistics Canada (2015b)

TPM, PM₁₀, PM_2.5, Pb, Cd: U.S. EPA (1998, 2010a)

Emission factors for TPM, PM₁₀ and PM_2.5 emitted by loading mixers and loading trucks: (U.S. EPA 2006)

PM₁₀ and PM_2.5 emission factors for sand and aggregate transfer are derived from a weighted combination of TPM emission factors, using information from the U.S. EPA’s PM Calculator database (2010a) (using SCC 30501101):

EF_PM10=0.51*EFM_TPM

EF_PM2.5=0.15*EF_TPM

Ferrous Foundries include facilities that produce castings of various types of ferro-alloys, as well as small iron and steel foundries not associated with integrated iron and steel facilities. The types of foundries found in Canada include open ferrous, electric arc and induction foundries.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO

Methodology under review.

The area source emissions were last estimated for 2011 and have been carried forward to 2015.

Methodology under review.

Methodology under review.

Rock, Sand and Gravel encompasses emissions from rock quarrying, stone processing, and sand and gravel operations.

Rock quarrying activities typically include the following sources: overburden removal, drilling in rock, blasting, loading of materials, transporting raw materials by conveyors or haulage trucks, scraping, bulldozing, grading, open storage pile losses, and wind erosion from exposed areas.

Stone processing is categorized into three activities, depending on the size of stone required: crushed stone, pulverized stone and building stone.

Sand and gravel deposits are quarried, transported to the plant, and then classified and stockpiled. Processing is accomplished by crushing, screening, washing, blending and stockpiling materials according to product specifications. Products are used for road construction, as an aggregate for asphalt and concrete, and for other construction purposes such as fill and mortar sand. Sand is also used in the glassmaking, foundry and abrasives industries.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Total quantity of rock, sand and gravel produced by province/territory is multiplied by pollutant-specific emission factors.

F. Menezes, Natural Resources Canada^Footnote7

Confidential provincial production values are estimated with population distributions: Statistics Canada (2016b)

TPM, PM₁₀, PM_2.5: EMEP/EEA (2013)

Silica Production applies to silica sand quarrying and processing mainly for the glass and refining and smelting industries. Industrial sand processing operations are similar to those of construction sand production, with dust emissions originating mainly from crushing and screening operations, especially when grinding to very fine particle sizes. Dry or wet screening and air classification may be carried out to achieve the desired size distribution. Both wet and dry methods of dust control are used, and baghouses are commonly used.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Total quantity of silica produced by province/territory is multiplied by pollutant-specific emission factors.

F. Menezes, Natural Resources Canada^Footnote8

Confidential provincial production values are estimated with population distributions: Statistics Canada (2016b)

TPM, PM₁₀, PM_2.5: EMEP/EEA (2013)

Refined Petroleum Products Bulk Storage and Distribution covers fugitive VOC emissions from bulk distribution terminals and bulk plants. It includes volatile components of fuels that are emitted as fuel moves from the refinery to the end user whenever tanks are filled or emptied or while tanks are open to the atmosphere, be they large above-ground tanks, tank trucks, or railcars. In addition, the subsector includes emissions that occur from the evaporation of fuels spilled during transfer operations.

Only fugitive VOC emissions from bulk plants are estimated as an area source.

Pollutant(s) Estimated:

VOCs

Emissions are calculated using the gross sales of gasoline for on-road motor vehicles multiplied by emission factors developed by Tecsult (2006).

Gross sales of gasoline for motor vehicles: Statistics Canada (2015a)

Study on gasoline vapour recovery in Stage 1 distribution networks in Canada: Tecsult (2006)

Natural Gas Distribution includes emissions from all infrastructure used to distribute natural gas to market.

Emissions from related construction activities, ancillary structures and operations (buildings, offices, etc.), and mobile sources are included under the Construction Operations, Commercial Fuel Combustion and Mobile Sources (respectively) of the APEI.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃

Emission estimates are generated with a comprehensive inventory and extrapolated based on production data (Environment Canada 2014, CAPP 2005)

Environment Canada 2014b, AER 2016, BCOGC 2016, CAPP 2016, CNLOPB 2016a, CNLOPB 2016b, CNLOPB 2016c, CNLOPB 2016d, CNLOPB 2016e, SK MOE 2016a, SK MOE 2016b, Statistics Canada 2016e, Statistics Canada 2016f

Environment Canada 2014

Natural Gas Transmission includes emissions from all infrastructure used to transport natural gas.

Emissions from related construction activities, ancillary structures and operations (buildings, offices, etc.) and mobile sources are included under the Construction Operations, Commercial Fuel Combustion and Mobile Sources (respectively) of the APEI.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃

Emission estimates are generated with a comprehensive inventory for 2011 and extrapolated based on production data (Environment Canada 2014, CAPP 2005).

Environment Canada 2014, AER 2016, BCOGC 2016, CAPP 2016, CNLOPB 2016a, CNLOPB 2016b, CNLOPB 2016c, CNLOPB 2016d, CNLOPB 2016e, SK MOE 2016a, SK MOE 2016b, Statistics Canada 2016e, Statistics Canada 2016f

Environment Canada 2014

The Upstream Petroleum Industry includes emissions from all infrastructure used to locate, extract, produce, process/treat and transport liquefied petroleum gas (LPG), condensate, crude oil, heavy oil and in situ crude bitumen to market. It also includes emissions from onshore and offshore facilities, as well as drilling and exploration, conventional oil and gas production, open pit mining and in situ oil sands production, natural gas processing and oil transmission. Specifically, this includes the following subsectors:

• Accidents and Equipment Failures
• Disposal and Waste Treatment
• Heavy Crude Oil Cold Production
• Light Medium Crude Oil Production
• Natural Gas Production and Processing
• Oil Sands In-Situ Extraction and Processing
• Petroleum Liquids Transportation
• Well Drilling/Servicing/Testing

Emissions from related construction activities, ancillary structures and operations (buildings, offices, etc.), and mobile sources are included under the Construction Operations, Commercial and Institutional Fuel Combustion, and Transportation and Mobile Sources (respectively) of the APEI.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃

Emission estimates are generated with a comprehensive inventory for 2011 and are extrapolated based on production data (Environment Canada 2014, CAPP 2005).

Environment Canada 2014, AER 2016, BCOGC 2016, CAPP 2016, CNLOPB 2016a, CNLOPB 2016b, CNLOPB 2016c, CNLOPB 2016d, CNLOPB 2016e, SK MOE 2016a, SK MOE 2016b, Statistics Canada 2016f

In addition to the extrapolated estimates, the SO_x estimates for Alberta are adjusted to account for regulations that were developed after the model was originally created. The adjustments are made with both historical provincial data and NPRI data. NPRI data for the Atlantic provinces are used in place of the model estimates due to the complete facility coverage for the region.  Additionally, extrapolated estimates for the Oil Sands In-Situ Extraction and Processing facilities are reconciled with NPRI data to eliminate double-counting.

Environment Canada 2014

Bakeries release VOCs during the leavening process of industrial baking. Emissions from products leavened by baking powder (used mainly for pastries) are negligible; however, VOCs are released when yeast is used for leavening. Yeast is used nearly exclusively in the production of bread and bread-like pastries.

Pollutant(s) Estimated:

VOCs

Total quantity of bread produced by province/territory is multiplied by an emission factor for VOCs.

Bread production values are estimated using:

• National bread/bakery product shipment values: Statistics Canada (2016a)
• Provincial bread/bakery product shipment values: Statistics Canada (2016c)
• Monthly Consumer Price Index (CPI) for Bread/Rolls and Flatbreads: Statistics Canada (2016c)

Cheminfo (2005)

EF_VOC = 2.35 kg per tonne of baked goods

Grain Processing covers emissions from grain elevators. Grain elevators are divided into four groups in the APEI:

Primary elevators receive grain by truck from producers for either storage or forwarding. These elevators sometimes clean or dry grain before it is transported to terminal or process elevators (U.S. EPA 1985).

Process elevators are grain processing plants or mills. While the elevator operations of unloading, conveying and storing are performed at these locations, direct manufacturing or processing of grain for use in other products are also carried out (U.S. EPA 1985).

Terminal elevators dry, clean, blend and store grain for shipment to transfer elevators, other terminals (for export) or process elevators.

Transfer elevators generally perform the same function as terminal elevators.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Total grain production by province/territory is multiplied by pollutant-specific emission factors through primary elevators, process elevators, transfer elevators and terminal elevators.

Annual grain production data by regions: CGC (2015)

Distribution of elevator throughputs: EC (1983)

Grain data: annual field crop production data by province (Statistics Canada 2015b, CANSIM, Table 001-0010).

TPM, PM₁₀, PM_2.5: Pinchin Environmental Ltd (2007)

Sawmills cover emissions from facilities that typically produce hardwood and softwood lumber from logs. The process of converting wet logs into dry lumber includes debarking, sawing, drying and planing steps, which all release air emissions.

Panel Board Mills include emissions from several types of mills, all producing hardwood and softwood-based materials. These include:

• Veneer and plywood mills
• Waferboard mills, consisting primarily of oriented strand board (OSB) mills
• Particle board and medium-density fiberboard (MDF) mills

Other Wood Products encompass emissions from furniture and cabinet manufacturers, wood treating plants, wood pellet mills and Masonite manufacturers.

The combustion of various fuels for energy production or waste disposal, notably wood residues, natural gas, liquefied petroleum gas (LPG) and fuel oil, is a common practice at wood products facilities. Significant amounts of air pollutant emissions result from combustion in this sector.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Sawmills and Panel Board Mills:

• TPM, PM₁₀ and PM_2.5: Estimation methodology makes use of the NPRI point source data in addition to a number of production indicators to estimate the PM of the facilities not reporting to the NPRI (Natural Resources Canada, Forest Products Association of Canada and the Composite Panel Association, corporate website information, annual reports, Resource Information Systems Inc. publications, Madison publications and occasional discussion with industry representatives);
• All other pollutants: Production rate estimates, hog fuel combustion data, and other fuel use data are used to estimate the area source emissions of the remaining pollutants (Meil et al. 2009; U.S. EPA 2014a).

The area source emissions were last estimated for 2014 and have been carried forward to 2015.

Other Wood Products:

All pollutants: Area source emissions are not calculated for this subsector. Rather, emissions are represented by point source data reported to the NPRI by the facilities themselves.

The area source emissions were last estimated for 2014 and have been carried forward to 2015.

NPRI 2014 data (EC 2015a) and data sources for facilities not reporting to the NPRI, including:

• Natural Resources Canada: Status of Energy Use in the Canadian Wood Products Sector (Meil et al. 2009)
• Forest Products Association of Canada annual reports (proprietary reports)
• Environment and Climate Change Canada’s Forestry Products Group
• RISI North American Wood Panels and Engineered Wood Products Capacity Report (RISI 2013)
• Madison’s 2014 Online Lumber Directory (Madison 2014)
• Verbal communications with industry representatives (unpublished)

Sawmills: U.S. EPA (2012a)

Plywood manufacturing, particle board, oriented strand board: U.S. EPA (1995b)

Fuel combustion: Meil et al. (2009); U.S. EPA (1992, 1995b, 2014a)

Air Transportation covers emissions from aircraft, but not airport support equipment (captured as off-road applications).

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, B(a)p, B(b)f, B(k)f, I(cd)p

Aircraft-specific activity (landing/take-offs) by province/territory is multiplied by pollutant-specific emission factors.

The emission estimates from Air Transportation are calculated using Aircraft Movement Statistics (Statistics Canada 2015d), a database developed by Statistics Canada based on flight-by-flight data, recorded at airport towers operated by NAV Canada post-1996 and Transport Canada pre-1996. The data are of the highest resolution available and are the only known such aircraft movement data within Canada.

For aircraft using turbo aviation fuel, hydrocarbon (HC), CO and NO_x emission factors are taken from the International Civil Aviation Organization (ICAO) databank (2009) or Hagstrom (2010) databank for landing/take-offs (LTO), and from EMEP/CORINAIR (2006) for the cruise stage. Emission factors are mapped to representative aircraft, based on engine characteristics. SO₂ is estimated as a sulphur balance, using data from the Sulphur In Liquid Fuels reports (EC 2013). The NH₃ emission factor is taken from Coe et al. (1996). Emissions of PM during LTO are based on a paper by Wayson et al. (2009), which relates the smoke number from the ICAO databank to an emission factor in g/kg fuel consumed.

For aircraft using aviation gasoline, VOC, CO, PM₁₀ and NO_x emission factors are taken from the Federal Office of Civil Aviation (FOCA 2007). No quantification of these emissions is performed at the cruise stage, due to a lack of emission factors. SO₂ is estimated as a sulphur balance, using data from the Sulphur In Liquid Fuels reports (EC 2013). The NH₃ emission factor is taken from Coe et al. (1996). PM_2.5 is calculated as 69% of PM₁₀ as per U.S. EPA (2005a). Lead is estimated as a lead balance, using the U.S. EPA’s 5% retention (U.S. EPA 2013). TPM is equal to PM₁₀ (U.S. EPA 2005a). Emissions of non-standard CACs are estimated as a ratio to PM₁₀ or HC/VOCs based on speciation profiles from the U.S. EPA (U.S. EPA 2005a).

Marine Transportation covers emissions from commercial marine vessels, but not recreational marine engines (captured as off-road applications).

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Vessel-specific activity (movements) is multiplied by pollutant-specific emission factors.

Vessel-specific movements: SNC-Lavalin Environment (2012)

SNC-Lavalin Environment (2012)

Due to the unavailability of activity data, emission estimates are calculated using linear interpolations for the years 2011 through 2014.

Emission factors originate from a variety of sources and are distinct per vessel type and dead weight tonnage, engine size and type, fuel type, and movement component (underway, anchor or berth). For this iteration of the APEI, the Marine Emission Inventory Tool (MEITv4.1) was used.

Emission factor sources, application and summaries are provided in section 3.3 of SNC-Lavalin Environment (2012). MEIT natively outputs hydrocarbon (HC), but not VOCs. An HC-to-VOC conversion rate is taken from U.S. EPA (2010c). Emissions of non-standard CACs are estimated as a ratio to PM₁₀ or HC/VOC, based on speciation profiles from the U.S. EPA (2005a).

On-road Vehicles include: Heavy-duty diesel vehicles, Heavy-duty gasoline trucks, Light-duty diesel trucks, Light-duty diesel vehicles, Light-duty gasoline trucks, Light-duty gasoline vehicles, Propane and natural gas vehicles, Motorcycles, and Tire Wear & Brake Lining.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Vehicle-specific activity (vehicle kilometres travelled) is multiplied by pollutant-specific emission factors in the MOVES model (version MOVES2014 was used for this submission).

Refuelling VOC emissions are included in under Service Stations.

Data on the vehicle fleet (counts), defined by fuel type, model-year and gross vehicle weight rating, originate from DesRosiers Automotive Consultants (DAC 2014) and R. L. Polk & Co. (Polk & Co. 2013) for light- and heavy-duty vehicles, respectively. Motorcycle populations originate from the publication Road Motor Vehicle, Trailer and Snowmobile Registration (registrations) (Statistics Canada 2013). The Annual Industry Statistics report (MMIC 2013) is used to estimate the age distribution of motorcycles by model year which is applied to motorcycle populations obtained from Statistics Canada.The actual activity level is vehicle kilometres travelled (VKT). To arrive at estimates of VKT, vehicle counts are multiplied by mileage accumulation rates from Stewart-Brown Associates (Stewart-Brown 2012).

Emission factors for on-road vehicles are embedded in the MOVES model. More information on MOVES is available online in the U.S. EPA user guides (U.S. EPA 2012b, 2014b) and in U.S. EPA technical guidance document (U.S. EPA 2010b).

Off-road Vehicles and Equipment consists of Off-road diesel vehicles and equipment and Off-road gasoline/LPG/CNG vehicles and equipment

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, B(a)p, B(b)f, B(k)f, I(cd)p

Application-specific activity (hours-of-use, load factor) is multiplied by pollutant-specific emission factors in the NONROAD model.

Data on the applications (vehicle/engine counts, load factor, hours-of-use), defined by fuel type, model year and source classification code, originate from EC (2011).

Off-road gasoline usage data: (ECCC 2016)

Emission factors for off-road applications are embedded in the NONROAD model. For this iteration of the APEI, NONROAD version 2012C was used. This version is based on the U.S. EPA’s NONROAD2008, and modified by Environment and Climate Change Canada to exploit detailed activity data. Model operation is conducted following the user guide for NONROAD2005/2008 (U.S. EPA 2005b), given that the functionality of the models is the same.

Emissions of non-standard CACs are estimated as a ratio to PM₁₀ or HC/VOC, based on speciation profiles in the SPECIATE4.2 database (U.S. EPA 2008). More information on the NONROAD model is available online.

Rail Transportation covers emissions from the fuel consumed by locomotive engines.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Railway activity (fuel consumption) is multiplied by pollutant-specific emission factors.

Fuel consumption data: Statistics Canada (2015c)

In 2013, the Rail Association of Canada (RAC) signed a Memorandum of Understanding (MOU) on locomotive emissions with Transport Canada for the period 2011-2015. Under the terms of the MOU, the RAC provides multiple datasets on the industry, including emission factors.

HC, CO, SO₂, PM₁₀ and NO_x emission factors are taken from RAC (2013). HC emissions are converted to VOCs using the method in U.S. EPA (2011). Ratios of PM₁₀ to PM_2.5 and TPM are taken from the U.S. EPA (U.S. EPA 2005a). The emission factor for NH₃ is taken from Coe et al. (1996). With the exception of dioxins/furans, emissions of non-standard CACs are estimated as a ratio to PM₁₀ or HC/VOCs, based on speciation profiles from U.S. EPA (2011). The dioxin/furan emission factor (0.54 ng/L) is taken from U.S. EPA (2006).

Animal Production reports emissions from the volatilization of NH₃ from nitrogen in manure, particulate matter that is released from feeding and housing, and non-methane volatile organic compounds (NMVOCs) that are released during livestock feeding, housing and manure management.

Ammonia volatilization is a chemical process that occurs when manure is excreted or stored without a cover. Once excreted, manure moves through a number of stages until it is eventually cycled back to farm fields. Ammonia volatilization occurs at each stage of this cycle, including: animal housing, transport to long-term storage, storage, and application of manure to the field.

Livestock production results in primary PM emissions as a result of the aerial transport of feed particles, feather fragments, fecal material, skin debris or dander, animal wastes, mould spores, bacteria, fungus, litter fragments, etc. Ventilation systems in livestock buildings are required for air exchange and, as a result, a portion of the PM in confined livestock buildings will be emitted into the atmosphere via the ventilation system.

NMVOC emissions from livestock production are the result of biological processes that partially break down feed during storage and digestion. Emissions from excreted manure occur during all stages of the manure management cycle. Sites of emission therefore include silage stores, livestock housing, manure stores, and agricultural fields on which manure is applied or that are used for grazing.

Pollutant(s) Estimated

TPM, PM₁₀, PM_2.5, NH₃, NMVOCs

The methodologies for ammonia emissions are developed by Environment and Climate Change Canada in collaboration with Agriculture and Agri-Food Canada (AAFC) through a national research project: the National Agri-Environmental Standards Initiative (NAESI).

Methods describing the estimates of NH₃ emissions from Canadian livestock are published for all major livestock categories (dairy, non-dairy, swine and poultry). Details on parameters used and animal category-specific methodologies are available from the following publications: Sheppard and Bittman (2010, 2012); and Sheppard et al. (2007a, 2007b, 2009a, 2009b, 2010a, 2011a; 2011b). Methodologies for minor animals, such as horses, goats, fur-bearing animals (mink, fox), wild boars, deer, elk, rabbit and poultry, were taken from Battye et al. (1994).

The methodologies for emissions of particulate matter from livestock production are developed by AAFC for publication in the National Agri-Environmental Health Analysis and Reporting Program (NAHARP), published every five years with the Agricultural Census. The method is consistent with the European Monitoring and Evaluation Programme (EMEP)/Core Inventory of Air Emissions in Europe (CORINAIR) Guidebook (EMEP/CORINAIR 2002), but uses country-specific emission factors. Methodologies are published in Pattey and Qiu (2012) and Pattey et al. (2015).

The methodology for estimating NMVOC emissions of  was based on tier 1 methodology outlined in the 2013 European Monitoring and Evaluation Programme/European Environment Agency Air Pollutant Emission Inventory Guidebook (EMEP/EEA, 2013).

Annual cattle, sheep and swine populations are calculated as the simple mean of semi-annual or quarterly surveys (Statistics Canada 2016f, 2016g). These smaller surveys are corrected to the Census of Agriculture (COA) population estimates that are collected every 5 years to ensure the accuracy of the estimates.

The populations of other livestock, such as horses, goats, bison, llamas and alpacas, deer and elk, wild boars, rabbits, and poultry, are taken from the COA exclusively, and annual populations are developed by linear interpolation in order to avoid large changes in census years. Where populations for certain alternative livestock animal categories were not available in the COA, values were held constant, or extrapolated back to zero.

The breeding mink and fox population estimates were taken from an annual Statistics Canada survey titled Supply and Disposition of Mink and Fox on Fur Farms (Statistics Canada 2016h). Rabbit populations were taken from responses to the COA as provided on the AAFC Red Meat Market website (AAFC 2016).

Ammonia:

Ammonia emission factors are a weighted average of a variety of different emission fractions that occur during the stages of the manure and animal production cycle.

The input to the emission factor equation originates from a combination of the Livestock Farm Practices Survey (LFPS), which defines feed distribution to and consumption by animals throughout the year, and generic parameters derived from scientific literature or expert opinion. This information is distributed spatially across Canada by ecoregion.

Animal populations are reassigned to a matrix of animal housing and manure management systems based on their relative proportion in the overall farm population.

The fractions of NH₃ emitted at each step in the manure cycle are taken in part from the European Monitoring and Evaluation Programme (EMEP)/Core Inventory of Air Emissions in Europe (CORINAIR) Guidebook (EMEP/CORINAIR 2002) and in part from Canadian studies. The resulting weighted emission factors are applied to populations of animal subcategories taken from census data at the ecoregion spatial scale.

Model to calculate NH₃ emissions: Sheppard et al. (2010a)

Particulate Matter:

Total particulate matter (TPM) emission factors for poultry are taken from Van Heyst (2005) and Van Heyst and Roumeliotis (2007). Emission factors for cattle and swine are average values from Takai et al. (1998) and Seedorf (2004). In the case of PM₁₀ and PM_2.5, emissions are estimated from TPM emission factors multiplied by 0.45 and 0.1 to produce PM₁₀ and PM_2.5 emission factors, respectively.

Average animal weights are used to convert emission factors in the form of g d^-1 AU^-1 to units of kg head^-1 year^-1

The emission factors for cattle are also assigned to the other animal types by assuming that the emission factors per animal unit for sheep, goats, bison, llamas, alpacas and horses are the same as those for cattle. Average body weight of cattle are consistent with information provided by Boadi et al. (2004) and with weight corrections for cattle according to the methodology outlined in the National Inventory Report: 1990-2013, Greenhouse Gas Sources and Sinks in Canada (EC 2015b). All other animal weights were consistent with values used to estimate nitrogen excretion in EC (2015b).

Currently no emissions are estimated for mink, fox, wild boars, deer, elk or rabbit.

Non-methane volatile organic compounds:

The emission factors for all animals were taken from Table 3-3 of EMEP/EEA (2013). For livestock categories where a choice of emissions factors was provided, the non-silage emission factor was selected, except for dairy cows and beef cattle in feedlots where the silage emission factor was used. A weighted emission factor for beef cattle was calculated using the fraction of time spent during each stage of production according to Boadi et al. (2004).

Fertilizer Application includes emissions emitted when synthetic nitrogen fertilizers are applied for annual and perennial crop production.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, NH₃

Ammonia:

The method is a simplified version of the approach adopted by Sheppard et al. (2010b) for application on an annual time step.

The methodology uses a regression model developed by Bouwman et al. (2002) and derived NH₃ emission factors, taking into account the most important parameters influencing emissions from synthetic nitrogen fertilizer application, based on a meta-analysis of scientific literature.

Particulates:

Methodology is under review.

Data on the types of nitrogen fertilizer used on farms are published by Statistics Canada (2015e).

Areas of seeded annual and perennial crops:

Statistics Canada (2015d) - CANSIM Table 001-0010 - Estimated areas, yield, production and average farm price of principal field crops, in metric units, annual, 1990 to 2015.

Soil properties, including pH and cation exchange capacity, are included in calculations by using soil polygon information from a national-scale spatial database describing the types of soils associated with landforms.

Ammonia emission factors are calculated using the multiple linear regression equation from Bouwman et al. (2002). The approach uses different regression parameters for synthetic nitrogen fertilizer types, method of nitrogen application, crop type, and soil pH and cation exchange capacity.

A matrix of emission factors for each combination of these conditions occurring across Canada is derived. The average provincial and national emission factors are weighted averages of the relative proportion of each combination of fertilizer type and fertilizer application practice on different soil types in different ecodistricts across the country.

TPM, PM₁₀ and PM_2.5 methodology is under review.

Agricultural harvest activities entrain particulate matter into the air. Particulate matter generated from agricultural harvesting, also known as grain dust, includes grain and dry plant particles, moulds, pollen and spores, silica, bacteria, fungi, insects and possibly pesticide residues. These emissions are generated by vehicles traveling over the soil or by the processing of plant materials by agricultural equipment.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Particulate matter emissions from agricultural harvest operations are computed by multiplying an emission factor and an activity factor relating emissions to the area harvested.

Activity data for PM emission estimates from crop harvesting rely on a combination of data from the Census of Agriculture and area estimates based on Earth Observation data. Activity data on areas of major field crops at an ecodistrict level from 1990 to 2015 are consistent with the data reported in the Agriculture and the Cropland remaining Cropland category of the Land Use, Land-use Change and Forestry sector for the National Inventory Report: 1990-2015, Greenhouse Gas Sources and Sinks in Canada (EC 2015).

Tillage practices produce PM emissions from mechanical disturbances such as seeding, seed bed preparation and cultivation.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Agricultural tillage is the common method used by farmers to prepare land for seeding and weed control. Particulate matter emissions are generated from airborne soil particles during tillage operations due to the mechanical disturbance of the soil surface.

Particulate matter emissions from agricultural tillage operations are proportional to the area tilled.  They are also dependent on the type of tillage practice as well as the number of tillage events per year. The calculations are described in more detail in Pattey and Qiu (2012).

The number of tillage events per year is dependent on tillage practices. There are fewer tillage events per year for conservation tillage compared to conventional tillage. Therefore, a reduction in particulate matter emissions from reduced tillage and no-till is observed.

Activity data for PM emission estimates from tillage practices rely mainly on a combination of data from the Census of Agriculture and area estimates based on Earth Observation analyses. Activity data on areas of major field crops, including summerfallow, and on tillage practices at an ecodistrict level from 1990 to 2015 are consistent with the data reported inthe Cropland remaining Cropland category of the Land Use, Land-use Change and Forestry sector for the National Inventory Report: 1990-2015, Greenhouse Gas Sources and Sinks in Canada (EC 2015).

Information on the number of tillage events per year for crop type and tillage practices is taken from soil cover indicators (Huffman et al. 2012).

Emission factors for tillage practices are calculated using the method in U.S. EPA (1985).

Wind erosion commonly occurs as wind blows across exposed agricultural land and results in PM emissions from the entrained particles.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Wind erosion emissions from agricultural lands are calculated by multiplying the cultivated cropland area by an emission factor.

Activity data for PM emission estimates from wind erosion rely mainly on a combination of data from the Census of Agriculture and area estimates based on Earth Observation data. Activity data on areas of major field crops, including summerfallow, and on tillage practices at an ecodistrict level from 1990 to 2015 are consistent with the data reported in the Cropland remaining Cropland category of the Land Use, Land-use Change and Forestry sector for the National Inventory Report: 1990-2015, Greenhouse Gas Sources and Sinks in Canada (EC 2015).

The PM emission factor for wind erosion is calculated using the wind erosion equation (Woodruff and Siddoway 1965), but considers the impact of soil and crop cover on PM emissions (Huffman et al. 2012). The emission factor for windblown PM emissions from agricultural lands is calculated using the methodology described in Pattey and Qiu (2012).

Agriculture - Fuel Use estimates includes emissions resulting primarily from external combustion sources used for space/water heating and crop drying.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Emissions are calculated for 10 types of fuel: natural gas, natural gas liquids, kerosene and stove oils, light fuel oil, heavy fuel oil, Canadian bituminous coal, sub-bituminous coal, lignite coal, anthracite coal and imported coal.

Total usage by fuel type and province/territory is multiplied by pollutant-specific emission factors.

Statistics Canada (2015c)

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO: U.S. EPA (1998)
(Emission factors are chosen to represent the typical type of combustion equipment for each fuel type.)

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO for natural gas fuel: U.S. EPA (2004a)
Sulphur contents of liquid fuels: EC (2010)
Sulphur contents of coal: CEA (2002)

NH₃: Battye et al. (1994); Coe et al. (1996)

Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f: CARB (2005); U.S. EPA (1998, 2003, 2004a)
(Emission factors are selected to represent the typical type of combustion equipment for each fuel type.)

Two sources of emissions are included under Cigarette Smoking:

1. Mainstream cigarette smoke, which is directly exhaled by the smoker
2. Sidestream smoke, which is directly released from burning cigarettes

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f

The average number of cigarettes smoked per year by the smoking population by province/territory is calculated and then multiplied by pollutant-specific emission factors.

Health Canada (2015); Statistics Canada (2014c)

Due to the unavailability of activity data, emission estimates for 2014 were carried over for 2015 and estimates for 1998 were calculated using linear interpolation.

TPM, PM₁₀, PM_2.5: Ott et al. (1996)

VOCs: Wallace et al. (1987)

CO: Ott et al. (1992)

NH₃: Roe et al. (2004)

Hg, Cd, Pb: Gray and Boyle (2002)

Dioxins/furans: U.S. EPA (2004b)

B(a)p, B(b)f, B(b)k: Ding et al. (2005)

Commercial and Institutional Fuel Combustion, Construction Fuel Combustion and Residential Fuel Combustion include emissions resulting primarily from external combustion sources used for space/water heating and material heating. Commercial establishments, health and educational institutions, government/public administration facilities, and residences all fall under these categories, in addition to construction sites.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Emissions are calculated for 10 types of fuel: natural gas, natural gas liquids, kerosene and stove oils, light fuel oil, heavy fuel oil, Canadian bituminous coal, sub-bituminous coal, lignite coal, anthracite coal and imported coal.

Total usage by fuel type and province/territory is multiplied by pollutant-specific emission factors.

Statistics Canada (2015c)

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO: U.S. EPA(1998)
(Emission factors are chosen to represent the typical type of combustion equipment for each fuel type.)

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO for natural gas fuel: U.S. EPA (2004a)

Sulphur contents of liquid fuels: EC (2010)

Sulphur contents of coal: CEA (2002)

NH₃: Battye et al. (1994) ; Coe et al. (1996)

Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f: CARB (2005); U.S. EPA (1998, 2003, 2004a)
(Emission factors are selected to represent the typical type of combustion equipment for each fuel type.)

Commercial Cooking includes emissions from cooking meat and French fries in commercial operations that are classified under five foodservice types: ethnic, fast food, family, seafood, and steak & BBQ. The types of meat considered include beef steak, hamburger, poultry with skin, poultry without skin, pork, seafood and other. Five types of commercial cooking equipment are taken into account including: chain driven charbroilers, underfired charbroilers, deep-fat fryers, flat griddles and clamshell griddles. The commercial operations inventoried are defined as all commercial foodservice points of distribution that are open to the public, offer prepared meals and snacks for consumption on/off-premises, and operate in a fixed location.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, VOCs, CO, B(a)p

Commercial Meat Cooking (1999 to 2014):

1. Determined the number of restaurants in each province/territory that were classified as ethnic, fast food, family, seafood, steak & BBQ.
2. Determined the fraction of restaurants with commercial cooking equipment (i.e. chain driven charbroilers, underfired charbroilers, deep-fat fryers, flat griddles and clamshell griddles), the average number of units of each type of equipment per restaurant, and the average amount of food cooked (i.e. steak, hamburger, poultry with skin, poultry without skin, pork, seafood and other) on each type of equipment.
3. Applied pollutant-specific emission factors to each type of food for each type of commercial cooking equipment to get the final emission estimates.

Commercial Meat Cooking (1990 to 1998):

Emission estimates for 1999 were back-casted to 1990 using the gross domestic product (GDP) for NAICS [72]: Accommodation and Food Services (Statistics Canada 2007).

Commercial Cooking of French Fries (1990 to 2014):

The annual national consumption rate of frozen fries was multiplied by the annual provincial/territorial population and by a VOC-specific emission factor.

All Commercial Cooking (2015):

Emission estimates for 2014 were carried forward to 2015 since 2015 activity data were not available.

Commercial Meat Cooking (1999 to 2014):

Activity data were estimated using:

• Annual restaurant census for Canada: ReCount Database (The NPD Group 2016)
• Statistics on the prevalence of commercial cooking equipment, for the five restaurant types (E.H. Pechan & Associates 2003)
• Statistics on the average number of pounds of meat cooked on each type of equipment per week for the seven types of meat (E.H. Pechan & Associates 2003)

Commercial Cooking of French Fries (1990 to 2014):

Activity data were estimated using:

• Provincial/territorial population data (Statistics Canada 2016b)
• Annual Canadian consumption rates of frozen fries (USDA Foreign Agricultural Service 2015)
• Assumed 80% of French fries were purchased in restaurants (E.H. Pechan & Associates 2003)

Commercial Meat Cooking:

TPM, PM₁₀, PM_2.5, VOCs, CO, B(a)p: E.H.Pechan & Associates (2003)

Commercial Cooking of French Fries:

VOCs: EF = 0.21 g/kg (E.H. Pechan & Associates 2003)

Home Firewood Burning encompasses emissions from wood burned in urban and rural homes for primary and supplementary heating, as well as for aesthetics and hot water, in both main and secondary residences. This covers household wood-burning devices such as wood-burning fireplaces, wood stoves, pellet stoves, outdoor boilers and a variety of other devices used in limited quantities, such as wood-fired cooking stoves.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

The quantity of wood burned by device type and province is multiplied by pollutant-specific emission factors by device type.

Activity data from Canadian Facts (1997, 2006) and TNS Canada (2012) are converted from volume to mass utilizing the reported wood species burnt. Wood consumption is interpolated and extrapolated from the three points (1996, 2006 and 2012) to the time series using statistical information on household wood-burning devices from Statistics Canada (1997, 2010) and Tracey (2014).

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃: Gulland (2000)

Pb, Cd, Hg, B(a)p, B(b)f, B(k)f: U.S. EPA (1995b)

Dioxins/furans: EC (2000)

Sources of emissions in the Human sector include respiration and perspiration.

Pollutant(s) Estimated:

NH₃

Annual population data by province/territory are multiplied by an NH₃ emission factor.

Statistics Canada (2015b)

Roe et al. (2004)

EF_NH3 = 0.0168 kg per person-year

Service Station estimates covers fugitive VOC emissions from fuel transfers and storage from refined petroleum products retail, as well as fugitive emissions from the refuelling of on- and off-road vehicles.

Off-road refuelling emissions include all non-vehicle gasoline usage (lawn mowers, snow blowers, etc.).

Pollutant(s) Estimated:

VOCs

Refined petroleum products retail

Emissions are calculated using gasoline usage data multiplied by emission factors for underground tank filling and breathing.

For British Columbia and Ontario, emissions from service stations are broken down into regulated versus unregulated areas. An emission control efficiency of 50% is applied to the filling of underground storage tanks in regulated areas in British Columbia and Ontario. The rest of the country is assumed to have no control efficiency.

Off-road refuelling

Off-road refuelling emissions are calculated using off-road gasoline usage data multiplied by an emission factor for uncontrolled vehicle refuelling.

On-road refuelling

On-road refuelling estimates are produced using the MOVES model. This year’s estimates were made using MOVES2014. Vehicle-specific activity (vehicle kilometres travelled) is multiplied by pollutant-specific emission factors.

Refined petroleum products retail: Gross sales of gasoline for motor vehicles: (Statistics Canada 2015b)

Off-road refuelling: Off-road gasoline usage data (ECCC 2016)

On-road refuelling: Data on the vehicle fleet (counts), defined by fuel type, model-year and gross vehicle weight rating, originate from DesRosiers Automotive Consultants (DAC 2014) and R. L. Polk & Co. (Polk & Co. 2013) for light- and heavy-duty vehicles, respectively.

Motorcycle populations originate from the Road Motor Vehicle, Trailer and Snowmobile Registration database (Statistics Canada 2013). The Annual Industry Statistics report (MMIC 2013) is used to estimate the age distribution of motorcycles by model year which is applied to motorcycle populations obtained from Statistics Canada. The actual activity level is vehicle kilometres travelled (VKT). To arrive at estimates of VKT, vehicle counts are multiplied by mileage accumulation rates from Stewart-Brown Associates (Stewart-Brown 2012).

Refined petroleum products retail and off-road refuelling: Evaporative emissions from gasoline service station operations (U.S. EPA 2008)

On-road refuelling: Emission factors for on-road vehicles are embedded in the MOVES model. More information on MOVES is available online, in the U.S. EPA user guides (U.S. EPA 2012b, 2014b) and in the U.S. EPA technical guidance document (U.S. EPA 2010b).

Emissions included under Other Miscellaneous Sources are from infant-diapered waste.

Pollutant(s) Estimated:

NH₃

An annual estimate of the population aged 0-3 years by province/territory is multiplied by an NH₃ emission factor.

Number of children aged 0-3 years by province/territory: Statistics Canada (2015a).

Roe et al. (2004)

EF_NH3 = 0.0136 kg of NH₃/person-year

Crematoriums clover emissions from the combustion of caskets and human bodies.

The combustion of fuel associated with the operation of a crematorium furnace or crematory fire is excluded from the sector. Fuel combustion emissions from cremations are captured under the Commercial Fuel Combustion sector.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, CO, Pb, Cd, Hg, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p, HCB

Number of human cremations per year by province/territory is multiplied by pollutant-specific emission factors.

Area source activity data is obtained from an annual report produced by the Cremation Association of North America (CANA): the Annual CANA Statistics Report 2012: Executive Summary (CANA 2013) and the draft Annual CANA Statistics Report (CANA 2016). Due to the unavailability of data, emission estimates are calculated using linear interpolation for all provinces/territories for the year 2001, and as well as Quebec for the years 2002-2007.

TPM, PM₁₀, PM_2.5: U.S. EPA (2014a)

VOCs, HCB: EMEP/EEA (2013)

SO_x, NO_x, CO: EMEP/EEA (2009)

Hg, Cd, Pb: U.S. EPA (2014a)

Dioxins/furans: U.S. EPA (2014a)

B(a)p, B(b)f, B(b)k, I(cd)p: U.S. EPA (2014a)

An average weight per body and casing of approximately 150 lbs. is assumed.

Industrial and Commercial Incineration involves the incineration of waste from industrial, commercial and institutional facilities. Emissions from the combustion of wood waste are included in Pulp and Paper Industry, Wood Products or Electric Power Generation.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg

Methodology under review.

The area source emissions were last estimated for 2011 and were carried forward to 2015.

Methodology under review.

Methodology under review.

The Municipal Incineration sector involves the incineration of domestic waste, as well as non-hazardous and industrial waste.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans

Methodology under review.

The area source emissions were last estimated for 2011 and were carried forward to 2015.

Methodology under review.

Methodology under review.

Landfills include emissions from disposal sites used for a variety of wastes, such as domestic, commercial, liquid and non-hazardous solid industrial wastes as well as sewage sludge. Disposal sites may be designated to receive only one or many of these waste materials. Materials deposited into landfills are covered daily with soil to prevent scattering of litter by wind, scavenging by animals, and odours. As a result, PM emissions are due to wind erosion, the movement of heavy vehicles and the dumping of waste.

The other main emissions from landfills include CH₄ and CO₂, with associated VOCs found in small concentrations in the fugitive landfill gas.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, VOCs

The quantity of waste landfilled for each province/territory is applied to PM emission factors.

VOC emissions are calculated as a concentration of the total fugitive landfill gas released, derived from CH₄ emissions.

Data for both provincial quantities of waste sent to landfills and CH₄ emissions from landfills were obtained from the Waste and Open Sources Section of the Pollutant Inventories and Reporting Division of Environment and Climate Change Canada.^Footnote9

CH4 emissions were estimated using the Landfill Air Emissions Estimation model, which is based on the Scholl Canyon model (U.S. EPA 1990)

TPM: BCMELP (1997)

PM₁₀, PM_2.5: GVRD and FVRD (2003). The EF_PM10 is calculated using a distribution percentage of 8% of the EF_TPM. The EF_PM2.5 is calculated using a distribution percentage of 2% of the EF_TPM.

VOCs: U.S. EPA (1995a). The default concentration of VOC in landfill gas is 835 ppmv.

Emissions from Residential Waste Burning are related to on-site burning of residential waste materials in backyard barrels or to open-pit burning in rural areas. 

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p, HCB

Methodology under review.

The area source emissions were last estimated for 2014 and were carried forward to 2015.

Methodology under review.

Methodology under review.

Other Incineration and Utilities applies to emissions from sewage sludge incineration and other small incinerators.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, Pb, Cd, Hg, dioxins/furans

Methodology under review.

The area source emissions were last estimated for 2011 and were carried forward to 2015

Methodology under review.

Methodology under review.

Dry Cleaning includes emissions from companies that provide dry cleaning of fabric and leather items.

General Solvent Use consists of emissions from a broad range of applications occurring in residential, commercial, industrial and institutional locations. Industrial applications include uses such as degreasing, adhesives and sealants, aerosols, blowing agents and resin manufacturing. The use of consumer and commercial products, pesticides and personal care products is also included under General Solvent Use.

Printing covers emissions from the manufacturing or use of printing inks. The sector consists of flexographic, gravure, letterpress, lithographic and other printing.

Surface Coatings encompasses emissions from a broad range of applications and industries, including individuals and companies engaged in the manufacturing or use of paints and coatings.

Pollutant(s) Estimated:

VOCs

The analysis methodology used is largely a “top-down” national mass balance approach that involves gathering statistical activity data on the production, distribution, end-use patterns and disposal of VOC-containing products, and then building relationships between stages. However, more detailed data on solvent quantities and practices are collected from a subset of solvent and formulated product users, producers and distributors in Canada.

Solvent use quantities (1990 to 2004): Cheminfo (2007)

Solvent use quantities (2005 to 2014): Cheminfo (2016a)

Twenty-nine commercially sold solvents, defined as VOCs under CEPA 1999, are inventoried.^Footnote10

Domestic consumption is determined using a national mass balance approach:

Consumption = Production + Imports - Exports +/- Inventory Changes

“Inventory changes” are a volume buffer between total supply (production and imports) and total demand (domestic consumption and exports) (Cheminfo 2016a). For most solvents, the value is zero because of a lack of detailed data on inventory changes (Cheminfo 2016a).

Information on production, trade and inventory changes is obtained from various literature sources, Statistics Canada and interviews with a subset of solvent producers and distributors.

Domestic consumption estimates are allocated to many reactive and emissive application areas. The default allocation basis in many cases is the historical distribution of solvent use from previous studies (Cheminfo 2016a). Survey questionnaire results, input from telephone consultations and literature sources are used to develop solvent use and VOC estimates for each solvent and application (Cheminfo 2016a).

Allocation to the provinces and territories is based on macroeconomic indicators, such as population, households and the gross domestic product (GDP) of commercial services and manufacturing (Cheminfo 2016a). For some industrial applications, specific allocations are derived from previous sector-specific studies (Cheminfo 2016a).

Projected estimates of national total solvent use for the year 2015 were developed based on historical base year national total solvent use and macroeconomic growth and solvent growth ratios (Cheminfo 2016b).

The estimated use of emission control technologies is applied in each solvent application area. More specifically, emissions are calculated by taking the estimated quantity of solvent used in an application area and multiplying it by the estimated percentage of uncontrolled VOCs or:

E_VOCs= Quantity_solventused ×(100%-% Controlled_VOCs)

where E_VOCs is the emission estimate of VOCs.

Emission controls (1990 to 2004): Cheminfo (2007)

Emission controls (2005 to 2014): Cheminfo (2016a)

If there is no estimated use of control technologies, then 100% of the solvent VOCs is assumed to evaporate.

Only a small portion of the estimated VOC emissions is reduced by the application of control technologies. Control efficiencies are applied (as percentages) in the following applications: flexographic, rotogravure and lithographic printing, aircraft coatings, automotive original equipment manufacture (OEM) coatings, metal can manufacturing, metal coil coating, metal furniture manufacturing, adhesives and sealants, and resin manufacturing (Cheminfo 2016).

Coal Transportation includes PM emissions resulting from the transportation of coal. Most of the coal mined in Canada is carried to trans-shipment or export terminals by unit trains. Coal imported into Canada is shipped in lake vessels. Some minor amounts of coal are shipped by truck (CCME 2001).

Load-in and load-out losses are estimated and reported by mine facilities to the NPRI as part of fugitive emissions. Emissions from fuel combustion during coal transport (diesel, gasoline or oil) are inventoried separately as part of the Mobile Sources category.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Average emission factors are derived from the quantities of coal transported, the distance travelled and the type of containment of the coal (control, closed environment, covered wagon, etc.) (CCME 2001). Resulting emission factors are multiplied by annual coal production by province/territory.

National and provincial coal production: NRCan (2015)

Monthly climate summaries: EC (2015c)

Monthly climate summaries: EC (2015c)

CCME (2001)

Construction Operations include PM emissions primarily resulting from soil disturbance on construction sites. The amount of soil disturbance is related to the surface area and duration of a construction project. The geographic region, type of construction (residential, industrial-commercial-institutional [ICI], engineering) and soil characteristics are all considered.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Methodology under review.

The area source emissions were last estimated for 2012 and are carried forward to 2015.

Methodology under review.

Mine Tailings covers emissions of particulates resulting primarily from wind erosion at mine tailings ponds located on active and inactive mine sites.

Concentrators used for mining produce both a finely-milled concentrate rich in the desired metal(s) and a solids-laden mine tailings stream. This slurry is sent to a tailings pond where the solids settle out of suspension and the supernatant solution is either recycled back in the process or discharged as effluent. It is common practice to keep the solids in the tailings pond submerged, even when the mine is inactive or closed. If the solids in the pond are no longer submerged, fugitive particulate emissions occur through wind dispersion.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Methodology under review.

The area source emissions were last estimated for 2005 and are carried forward to 2015.

Methodology under review.

Methodology under review.

Emissions from the Paved Road Dust sector originate from primary and secondary (re-suspended) PM emissions.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Primary emissions are produced by multiplying the total vehicle kilometers travelled for each province/territory by pollutant-specific emissions factors.

The methodology for secondary (re-suspended) emissions is currently under review. The emissions were last estimated for 2002 and have been carried forward to 2015.

Primary - Vehicle kilometres travelled (VKT) are estimated by multiplying vehicle counts by mileage accumulation rates from Stewart-Brown Associates (Stewart-Brown 2012).

Primary - EMEP/EEA (2013)

Secondary - Methodology under review.

Emissions from the Unpaved Road Dust sector originate from re-suspended PM emissions.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5

Methodology under review.

The area source emissions were last estimated for 2002 and have been carried forward to 2015.

Methodology under review.

Methodology under review.

Prescribed Forest Burning includes emissions from controlled fires used for land management treatments. Prescribed burning is used to reduce logging residues, manage forest production, control insects and minimize potential for destructive wildfires. The practice of prescribed burning is carried out by the logging industry and forestry officials to manage Crown lands. This sector excludes the burning of agricultural residues.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃, dioxins/furans, B(a)p, B(b)f, B(k)f, I(cd)p

Total annual mass of forest debris burned by fire and by province/territory is multiplied by pollutant-specific emission factors.

The total number of hectares burned in each province/territory per year (CIFFC 2016; PCA 2016; NFD 2016) is multiplied by a conversion factor for each province/territory (EC 1992) to convert the area burned into the mass of forest debris burned. Pollutant and province-specific emission factors are then applied to the mass of forest debris to determine the release of pollutants from the burn.

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃:

All provinces/territories (except British Columbia): U.S. EPA (1995a)

British Columbia: GVRD and FVRD (2003), BCMWLAP (2004).

Dioxins/furans, B(b)f, B(k)f: Lemieux et al. (2004)

B(a)p, I(cd)p: Johnson et al. (1992)

Structural Fires cover emissions from vehicle fires (such as fires from cars, trains and airplanes) and fires that burn buildings. Structural fires emit large quantities of pollutants due to rapid but incomplete combustion.

Pollutant(s) Estimated:

TPM, PM₁₀, PM_2.5, SO_x, NO_x, VOCs, CO, NH₃

Tonnes of structures burned per year, by province/territory, are multiplied by pollutant-specific emission factors.

The Secretary/Treasurer of the Council of Canadian Fire Marshals and Fire Commissioners^Footnote11 (CCMFC) and the following members of the CCMFC are contacted to obtain the number of annual structural fires in their jurisdictions:

• Government of Nunavut^Footnote12
• Fire and Emergency Services, Newfoundland and Labrador^Footnote13
• Office of the Fire Marshal and Emergency Management (Ontario)^Footnote14
• Office of the Fire Commissioner (Manitoba)^Footnote15
• Emergency Management and Fire Safety Branch (Saskatchewan)^Footnote16
• Canadian Forces Fire Marshal^Footnote17
• Office of Public Safety (Prince Edward Island)^Footnote18
• Yukon Government^Footnote19
• Department of Labour and Advanced Education (Nova Scotia)^Footnote20
• Department of Municipal and Community Affairs (Government of the Northwest Territories)^Footnote21
• Department of Public Safety (New Brunswick)^Footnote22
• Office of the Fire Commissioner (Alberta)^Footnote23
• Emergency Management British Columbia^Footnote24
• Ministère de la Sécurité publique^Footnote25

Number of structure fires in each province/territory is multiplied by a loading factor to convert the number of fires into tonnes of structure burned (EIIP 2001). 

Loading factor = 1.04 t of structure burned/fire

Due to the unavailability of activity data, emission estimates for 2001, 2002 and 2004 are calculated using linear interpolation.

TPM, PM₁₀, PM_2.5, NO_x, VOCs, CO: GVRD and FVRD (2003)

NH₃: Battye et al. (1994)

Mercury in Products covers emissions from Hg contained in products throughout their life cycle from manufacture to final disposition. The following products are included:

• Automotive switches
• Switches and relays
• Batteries
• Dental amalgams
• Fluorescent tubes
• Non-fluorescent lamps
• Measurement and control devices
• Thermometers
• Thermostats
• Tire balancers

Emissions from the above devices impact the following sectors/subsectors:

• Iron and Steel Industries - (Secondary) Electric Arc Furnaces
• Iron and Steel Industries - Steel Recycling
• Electronics
• Other Manufacturing
• Municipal Incineration
• Other Incineration
• Human
• Other Miscellaneous Sources
• Landfills
• Water and Sewage Treatment
• Residential Waste Burining

Pollutant(s) Estimated:

Hg

Methodology under review.

The area source emissions were last estimated for 2008 and have been carried forward to 2015.

Methodology under review.

Methodology under review.