TECHNICAL SUPPORT DOCUMENT FOR 

EMISSIONS FROM ELECTRIC EQUIPMENT 

MANUFACTURE OR REFURBISHMENT AND 

MANUFACTURING OF ELECTRICAL 

COMPONENTS 

 PROPOSED RULE FOR MANDATORY 

REPORTING OF GREENHOUSE GASES 

Office of Air and Radiation 

U.S. Environmental Protection Agency 

March 22, 2010 

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Contents

1. Source Description...............................................................................................................................................3 

a. Total U.S. Emissions.......................................................................................................................................3 

b. Emissions to be Reported................................................................................................................................3 

2. Options for Reporting Threshold .........................................................................................................................4 

a. Data Analysis Supporting Proposal.................................................................................................................4 

3. Options for Monitoring Methods.........................................................................................................................5 

a. IPCC Tier 1 Approach.....................................................................................................................................5 

b. IPCC Tier 2 Approach.....................................................................................................................................5 

c. IPCC Tier 3 Approach.....................................................................................................................................5 

4. Issues Related to the Transfer of Equipment from Equipment Manufacturers to Equipment Users....................9 

5. Review of Existing Relevant Reporting Programs/Methodologies....................................................................10 

6. Procedures for Estimating Missing Data............................................................................................................10 

7. QA/QC Requirements........................................................................................................................................10 

8. Reporting Procedures.........................................................................................................................................11 

9. References..........................................................................................................................................................11 

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1. Source Description 

Sulfur hexafluoride (SF6) is most commonly used in the electrical power industry where it acts as an insulator and 

interrupter in equipment that transmits and distributes electricity (RAND 2004). The electric power industry in the 

United States has used SF6 gas since the 1950s because of its superior dielectric strength and arc-quenching 

characteristics. SF6 has replaced flammable insulating oils in many applications and allows for more compact 

substations in dense urban areas. Currently, there are no available or foreseen substitutes for SF6. 

 

High-voltage circuit breakers account for the majority of SF6 use in the United States. Other types of electrical 

equipment that use SF6 include gas-insulated substations, switches (other than circuit breakers), high-voltage 

transmission lines, and high-voltage bushings. 

Original equipment manufacturers (OEMs) purchase bulk SF6 gas to: 

 install a shipping charge in high-voltage closed-pressure equipment;1

 ship alongside closed-pressure equipment for topping off at installation site; 

 fill sealed-pressure equipment with its intended lifetime supply of SF6;

2

 and 

 test equipment. 

SF6 emissions from OEMs typically occur during the testing manufacturing, and installation or commissioning of 

equipment but can also occur when equipment is decommissioned at a manufacturing facility. 

Perfluorocarbons (PFCs) are sometimes used as dielectrics and heat transfer fluids in power transformers. PFCs are 

also used for retrofitting CFC-113 cooled transformers. One PFC used in this application is perfluorohexane 

(C6F14). In terms of both absolute and carbon-weighted emissions, PFC emissions from electrical equipment are 

generally believed to be much smaller than SF6 emissions from electrical equipment; however, there may be some 

exceptions to this pattern (IPCC, 2006). Throughout this Technical Support Document, “SF6” will be used to denote 

SF6 and/or PFCs. 

a. Total U.S. Emissions 

Emissions of SF6 from OEMs in the United States were estimated to be 0.8 Tg CO2 Eq. in 2006 (EPA 2008). 

The 1990 to 2006 emission estimates for OEMs were derived by assuming that manufacturing emissions equal 10 

percent of the quantity of SF6 charged into new equipment. The quantity of SF6 charged into new equipment from 

1990 to 2000 was estimated based on statistics compiled by the National Electrical Manufacturers Association 

(NEMA). The quantities of SF6 charged into new equipment for 2001 to 2006 were estimated using data reported by 

participants in EPA’s SF6 Emission Reduction Partnership for Electric Power Systems along with EPA’s estimate of 

the total industry SF6 nameplate capacity (128.4 Tg CO2 Eq. in 2006). Specifically, EPA calculated the ratio of new 

nameplate capacity to total nameplate capacity of a subset of Partners for which new nameplate capacity data was 

available from 1999 to 2006. EPA then multiplied this ratio by the total industry nameplate capacity estimate to 

derive the amount of SF6 charged into new equipment for the entire industry. The 10 percent emission rate is the 

average of the “ideal” and “realistic” manufacturing emission rates (4 percent and 17 percent, respectively) 

identified in a paper prepared under the auspices of the International Council on Large Electric Systems (CIGRE) in 

February 2002 (O’Connell et al. 2002). This method for estimating OEM emissions is the same method used in 

EPA’s Inventory of Greenhouse Gas Emissions and Sinks:1990-2006 (EPA 2008). 

b. Emissions to be Reported 

 

1

 Closed-pressure equipment requires refilling (topping up) gas during its lifetime and generally contains between 

five and several hundred kilograms of SF6 per unit (IPCC 2006). 2

 Sealed-pressure equipment should not require any refilling (topping up) with gas during its lifetime and generally 

contains less than 5 kilograms of SF6 per unit (IPCC 2006). 

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EPA is requiring facilities to report all SF6 and PFC emissions from testing and manufacturing of new equipment, 

from refurbishing and decommissioning of previously manufactured equipment, and in certain circumstances from 

installation of new equipment. 

2. Options for Reporting Threshold 

EPA evaluated a range of emission and consumption-based thresholds for electrical equipment manufacturing. The 

emission-based thresholds considered were 1,000; 10,000; 25,000; and 100,000 mt CO2 Eq. These thresholds 

translate to consumption-based thresholds of 922; 9,220; 23,061, and 92,244 lbs of SF6, respectively, assuming an 

average manufacture emission rate of 10%. 

As shown in Table 1 below, EPA estimates that all ten domestic facilities identified as consumers of SF6 will fall 

above the 1,000; 10,000; and 25,000 mt CO2 Eq. thresholds and above the 922; 9,220; 23,061 lbs. of SF6 thresholds, 

while only the largest five facilities would be captured by the 100,000 mt CO2 Eq./92,244 lbs SF6 threshold. 

However, while EPA attempted to accurately estimate SF6 consumption per facility, it is conceivable that OEMs 

specializing in the production of relatively low-voltage switchgear for the distribution market will fall below the 

consumption threshold. 

Additional details on the number of facilities and total emissions that would be captured by each threshold are 

shown below in Table 1. 

Table 1. Emission Threshold Summary 

Emission Threshold (Mt CO2 Eq) 1,000 10,000 25,000 100,000 

Consumption Threshold (lbs. of SF6) 922 9,220 23,061 92,244 

Number of Facilities Above 10 10 10 5 

Percent of Facilities Above 100% 100% 100% 50% 

Total Emissions of Facilities Above (Mt CO2 Eq) 814,128 814,128 814,128 569,890 

Percent of Emissions Above 100% 100% 100% 70% 

a. Data Analysis Supporting Proposal 

 

The consumption-based threshold offers an important advantage relative to the emission-based threshold because it 

permits OEMs to quickly determine whether they are covered. It also avoids the scenario in which sources drop in 

and out of the program based on fluctuating emissions. 

EPA performed a threshold analysis to determine how many OEMs would fall above and below the four different 

consumption thresholds considered. The analysis was performed by: 

 Using the Inventory of U.S. Greenhouse Gas Emissions and Sinks: 1990-2006 (EPA 2008) to determine the 

estimated amount of SF6 gas purchased by all OEMs, which was estimated as 750,981 lbs in 2006. 

 Converting the 750,981 lbs of SF6 to metric tons of CO2 equivalent, which is 8,141,281 Mt CO2 Eq. 

 Estimating total U.S. emissions by multiplying total purchases by the 10% emission rate, which is 814,128 

Mt CO2 Eq. 

 Identifying the ten OEMs in the U.S. that are responsible for most of the SF6 consumption in the 

manufacturing sector. 

 Dispersing the total amount of U.S. OEM emissions of SF6 among each of the ten OEMs based on the 

estimated market-share of each OEM. 

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3. Options for Monitoring Methods 

For electrical equipment manufacturers, emissions can occur during equipment testing, manufacturing, installation, 

and decommissioning and refurbishing. EPA evaluated a range of options for estimating emissions that result from 

these activities. The three primary options reviewed were the Tier 1, Tier 2, and Tier 3 IPCC methods presented in 

the 2006 IPCC Guidelines for National Greenhouse Gas Inventories (IPCC 2006). Each of these options is 

described below. 

a. IPCC Tier 1 Approach 

The Tier 1 method, referred to as the default emission factor method, estimates emissions by multiplying the 

appropriate default regional emission factor by the amount of SF6 consumed by each equipment manufacturer. 

Tier 1 emission factors are usually developed through industry research. However, due to a lack of data availability, 

IPCC does not provide a default emission factor for the United States. The default emission factors for emissions 

associated with the manufacture of closed-pressure electrical equipment in Europe and Japan are 8.5% and 29%, 

respectively. 

b. IPCC Tier 2 Approach 

The Tier 2 method, referred to as the country-specific emission factor method, also uses emission factors. But these 

emission factors are more accurate than the Tier 1 factors because they are developed using criteria specific to the 

country where the manufacturer is located and are usually developed by analyzing actual pure-mass balance 

emissions that were calculated at the life-cycle level. 

While the Tier 1 and Tier 2 approaches are relatively simple, they are likely to result in inaccurate facility emissions 

estimates because they do not take into account the variation in SF6 handling and management practices among 

OEMs as well as variation in production methods associated with the different types of electrical equipment 

produced. Furthermore, due to lack of data availability, IPCC does not provide emission factors for electrical 

equipment manufacturing in the United States. 

c. IPCC Tier 3 Approach 

The Tier 3 method measures SF6 emissions using mass-balance equations for each life-cycle stage of the SF6 use. 

The equations below are based on the Tier 3 mass-balance equations for equipment manufacturing emissions and 

equipment installation emissions. 

The Tier 3 equation for estimating emissions from equipment manufacturing emissions, which includes equipment 

testing, equipment manufacturing, and equipment decommissioning and refurbishing is the following: 

 

Equipment Manufacturing Emissions = Decrease in SF6 Inventory + Acquisitions of SF6 – 

Disbursements of SF6

Where: 

Decrease in SF6 Inventory = SF6 stored in containers at the beginning of the year – SF6 stored in 

containers at the end of the year 

Acquisitions of SF6 = SF6 purchased from chemical producers or distributors in bulk + SF6 returned 

by equipment users or distributors with or inside equipment + SF6 returned to site after off-site 

recycling 

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Disbursements of SF6 = SF6 contained in new equipment delivered to customers + SF6 delivered to 

equipment users in containers + SF6 returned to suppliers + SF6 sent off-site for recycling + SF6 

destroyed 

In addition, emissions may occur when the manufacturer fills the equipment offsite from the manufacturing facility, 

before transferring custody to the equipment user. These emissions, along with other issues related to the transfer of 

equipment from manufacturers to users, are discussed further below. 

To quantitatively determine disbursements of SF6 to customers in new equipment (or cylinders), four options were 

considered: 

 Option 1: Disbursements could be estimated by weighing containers before and after gas from the 

containers was used to fill equipment or cylinders. 

 Option 2: Disbursements could be estimated by using flow meters to measure the amount of gas used to fill 

equipment or cylinders. 

 Option 3: Disbursements could be estimated by assuming that the mass of SF6 or PFCs disbursed to 

customers in equipment is equal to the nameplate capacity of the equipment or, where the equipment is 

shipped with a partial charge, equal to the nameplate capacity of the equipment times the ratio of the 

densities of the partial charge and the full charge. 

 Option 4: Disbursements could be estimated by weighing the equipment filled with SF6 or the PFC from 

the container before and after filling. The tare weight of the equipment would then be subtracted from the 

weight of the filled equipment to determine the weight of the gas in the equipment, and therefore, the 

weight of the actual disbursement. 

These options and their advantages and disadvantages are discussed, in turn, below. 

 Option 1 appears to be a practice currently employed at some manufacturing facilities. A digital scale is 

used to weigh the containers storing the gas before and after the equipment is filled (MEPPI 2010). In this 

regard, this option does not present new costs or changes to current procedures. However, EPA recognizes 

that emissions can occur downstream of the container to the equipment being filled. These emissions can 

occur through leaks in the hose or line connecting the container to the equipment, during coupling and 

decoupling activities, as well as through general mishandling (e.g., a faulty connection). To accurately 

estimate disbursements, these emissions should be estimated separately and subtracted from the 

disbursement total. These emissions could be estimated using measurements and/or engineering 

assessments or calculations based on chemical engineering principles or physical or chemical laws or 

properties. Such assessments or calculations could be based on, as applicable, the internal volume of the 

hose or line that is open to the atmosphere during coupling and decoupling activities, the internal pressure 

of the hose or line, the time the hose or line is open to the atmosphere during coupling and decoupling 

activities, the frequency with which the hose or line is purged and the flow rate during purges. Such 

methods could also include the use of leak detection methods (e.g., EPA Method 21 and the Protocol for 

Equipment Leak Emission Estimates) to determine a loss factor appropriate to calculate emissions. 

Unexpected or accidental emissions from the filling lines or hoses should be included in the total. EPA’s 

understanding is that electrical equipment is at a vacuum and is sealed prior to being filled with SF6 or 

PFCs (MEPPI, 2010). However, if any air or nitrogen is in the equipment and is purged during the filling 

process, then the method should also account for SF6 and PFC emissions that occur during such purging. 

 Option 2 presents the same issue as in option 1 in that emissions downstream of the containers would be 

required to be estimated separately and subtracted from the disbursement total. One disadvantage in this 

approach is that flow meters may not be used by the OEM, in which case, the OEM would need to purchase 

these devices. OEMs commonly rely only on the pressure rise to monitor the transfer of the gas from a 

container to a breaker or other piece of equipment (MEPPI 2010). 

 Option 3 equates the mass of SF6 or PFCs disbursed to customers in equipment to the nameplate capacity 

of the equipment or, where the equipment is shipped with a partial charge, equal to the nameplate capacity 

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of the equipment times the ratio of the densities of the partial charge and the full charge. The nameplate 

capacity could be based on the manufacturer’s current estimate (i.e., the one that appears on the nameplate) 

or it could be measured. One disadvantage of assuming that the mass of SF6 or PFCs disbursed to 

customers in equipment is equal to the current estimate of the nameplate capacity is that the current 

estimate may never have been measured with good precision and accuracy. Even if the nameplate capacity 

has previously been carefully measured, the internal volume of the equipment or density to which the 

equipment is charged might have changed since the original measurement. Because the mass-balance 

approach requires precise inputs, inaccuracies of even two or three percent could lead to very large 

inaccuracies in the facility’s emissions estimate. 

One way of developing a more precise estimate of the nameplate capacity of equipment would be to fill the 

equipment with a fluid and then to carefully recover the fluid, measuring what was recovered. This fluid 

could be SF6, another gas, or a liquid. If SF6 was used, the equipment would be charged to its operational 

or shipping SF6 density using the facility’s usual methods and then emptied. The mass of the SF6

recovered, adjusted slightly for the residual pressure of the SF6 that would remain in the equipment even at 

a deep vacuum, could be equated to the full or shipping charge, as applicable. One advantage of this 

approach is that it would reflect the actual SF6 charging practices of the facility; one disadvantage is that it 

could result in small SF6 emissions during the charging and recovery steps. 

If a liquid was used, the equipment would be filled carefully, ensuring that the full volume was filled, and 

then emptied. The volume of the liquid recovered would be equated to the internal volume of the 

equipment. The temperature of the liquid would need to be kept constant throughout this exercise to obtain 

an accurate measurement of the volume. This volume multiplied by the SF6 density at the full charge would 

yield the nameplate capacity of the equipment. 

To account for variability, a certain number of these measurements would need to be performed to develop 

a robust and representative average nameplate capacity (or shipping charge) for each make and model. 

Equipment samples should be selected so as to reflect predictable variability in the facility’s filling 

practices and conditions.3

 In addition, within a particular set of conditions, equipment should be selected at 

random. The specific number of samples would depend on the variability of the nameplate capacity within 

each make and model and on the desired level of precision of the estimated mean nameplate capacity of 

each make and model. As discussed below, the desired level of precision of the mean would depend on the 

level of precision of the emissions estimate as a whole. 

A Student T distribution calculation is the appropriate statistical procedure for determining when additional 

samples should be taken to achieve a tolerable error for the average nameplate capacity of a certain make 

and model of SF6-containing electrical equipment.4

 The calculation presumes an approximately normal, 

bell-shaped distribution of the underlying parameter, which implies that the distribution of the average is 

the Student’s t distribution. In principle, the mean of the samples taken approaches the true mean as more 

samples are taken; this procedure determines how many samples are needed as a function of the relative 

standard deviation of the sample measurements. The following matrix demonstrates this concept using a 

95 percent confidence level and an assumed initial sample size of ten. On the left is the relative standard 

deviation of the sample population; an initial sample size of ten was chosen for this computation.5

 For 

example, an equipment manufacturer conducts a minimum of ten tests to determine the nominal nameplate 

capacity of ten samples from a given make and model of a high voltage circuit breaker. In this hypothetical 

example, the resulting standard deviation of those samples is 1.5 percent. If the tolerable error is one 

 

3

 For example, if equipment is filled to a particular pressure, and the temperature of the facility varies during the day 

or seasonally, then the density to which the equipment is filled will vary as well (with higher densities at lower 

temperatures). In this case, samples should be taken to reflect the typical range of temperatures at which equipment 

is filled. 

4

 See the Technical Support Document for Fluorinated Gas Production for more discussion of the Student’s t test. 

5 Table 2 is provided as an example; a manufacturer would apply the Student T distribution to determine the 

appropriate number of samples based on the variability of the quantity of gas charged into equipment of a given 

make and model. 

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percent of the true mean, the manufacturer must increase its sample size to twelve, i.e., conduct two more 

tests, according to the chart below. If the standard deviation of the sample population tested was larger, the 

number of samples that would need to be taken would also increase.6

 

Table 2. Example Lookup Table of Total Sample Size required to 

meet Precisions, given Initial Sample Size of 10 

 Precision 

 0.25% 0.50% 1.00% 5.00% 

0.5% 18 10 10 10 

1.0% 64 18 10 10 

1.5% 141 38 12 10 

2.0% 249 64 18 10 

2.5% 389 99 27 10 

3.0% 560 141 38 10 

3.5% 763 191 50 10 

4.0% 996 249 64 10 

4.5% 1260 315 81 10 

Relative Standard Deviation of Sample 

5.0% 1556 389 99 10 

The actual precision with which the mean nameplate capacity would need to be measured would depend on 

(1) the desired level of precision for the emissions estimate for the facility, (2) the precision with which the 

other quantities in the mass-balance equation were monitored, (3) the share of the facility’s SF6

disbursements accounted for by a particular make and model, (4) the number of makes and models whose 

nameplate capacities were measured,7

 and (5) the level of emissions. Example calculations indicate that a 

facility that measured gas acquisitions with a precision and accuracy of one percent and that had an 

emission rate of 10 percent might need to estimate the mean nameplate capacity (or shipping charge) to a 

precision of two percent to achieve a precision in its emissions estimate of about 20 percent (expressed as a 

95-percent confidence interval). A facility that measured gas acquisitions with a precision and accuracy of 

one percent and that had an emission rate of 5 percent might need to estimate the mean nameplate capacity 

to a precision of one half of one percent to achieve a precision in its emission estimate of about 25 percent. 

(The accuracy of the device used for the nameplate capacity measurement would also need to be one half of 

one percent or better.) 

For other sources (e.g., fluorinated GHG production processes using the mass-balance approach), EPA is 

proposing a maximum error of 30 percent. However, in general, the tolerable level of error in an estimate 

depends in part on the size of the emissions. For smaller emission sources, errors larger than 30 percent 

might be tolerable. 

 

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 It is important to note that the reliability of the mean nameplate capacity estimate depends on the accuracy and 

precision of the individual measurements as well as on the number of times they are repeated. Accuracy is a 

measure of the bias (systematic error) of a measurement; precision is a measure of the random error. The precision 

includes the random errors from the measuring devices such as the scales used and the variation in the nameplate 

capacity for a single make and model. Repeated measurements using the same measurement device improve the 

precision of the mean, but they do not improve accuracy because each measurement has the same systematic error. 

For example, if the scale used to weigh the SF6 shipping charges is only guaranteed to be accurate within one 

percent, and it happens to be biased upward by 0.75 percent, the mean of even 2,000 weight measurements of the 

same device will be biased upward by 0.75 percent. 

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 If the nameplate capacities of multiple models were measured independently, using multiple measurement devices, 

then the “error” (more precisely, the relative standard deviation) of their summed or averaged nameplate capacities 

would be smaller than the errors of their individual nameplate capacities. However, if the nameplate capacities were 

measured using the same measuring device (with the same systematic error), then the error of the summed 

nameplate capacities would not be reduced below the systematic error of the individual nameplate capacity 

measurements. 

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To reflect subtle changes in manufacturing methods and conditions over time, it may be appropriate to 

require re-measurement of nameplate capacities at some interval, e.g., every five or ten years. 

According to industry, equipment manufacturers are filling breakers with SF6 gas to a full charge as part of 

their testing procedures; the equipment is then evacuated and filled to a partial charge for shipment at a 

later stage in the process (MEPPI 2010). Therefore, an advantage to this option is that it appears that it 

could be integrated into normal facility procedures without introducing any significant filling and 

recovering related activities. However, if the test charge were used to estimate the nameplate capacity, 

equipment manufacturers would need to account for possible variations between the density to which the 

equipment was charged during the test and that to which it was charged for shipping. 

 Lastly, Option 4 would require the weighing of the equipment filled with SF6 or the PFC before and after 

the equipment is charged. The tare weight of the equipment would then be subtracted from the weight of 

the filled equipment to determine the weight of the gas in the equipment, and therefore, the weight of the 

actual disbursement. Although, in theory this option is advantageous because it shifts the emphasis to the 

equipment that is being disbursed (rather than weighing the containers at the intermediary step), this option 

is not practical for two reasons. First, the mass of the SF6 or PFC charged into the equipment is likely to be 

low relative to the mass of the equipment; thus, it may be difficult to obtain a precise measurement of the 

mass of the SF6 or PFC using this method (i.e., within 1 percent) even if the scale is precise and accurate to 

within 1 percent of full scale. Second, it would be very difficult and impractical to weigh the shipping unit, 

which can be large and difficult to maneuver onto a scale (MEPPI 2010). 

4. Issues Related to the Transfer of Equipment from Equipment Manufacturers to 

Equipment Users 

As noted above, emissions may occur when the manufacturer fills the equipment offsite from the manufacturing 

facility, before transferring custody to the equipment user. Such emissions could be estimated using the following 

equation: 

Equipment Installation Emissions (offsite from OEM facility) = SF6 used to fill equipment offsite 

(from the OEM facility) + SF6 charged into the equipment at the OEM facility – Nameplate 

capacity of equipment installed offsite (from the OEM facility) 

These emissions could be attributed to the equipment manufacturer. In addition, any emissions from equipment that 

was filled (partially or completely) at the OEM’s facility but whose charge leaked out before being delivered to and 

installed for the customer could also be the manufacturer’s responsibility to report. 

EPA understands that in some cases, manufacturers may deliberately exceed the nameplate capacity of equipment 

when charging it, e.g., to postpone the re-fill of the equipment in the event that the equipment develops a leak. If 

this is the case, then the actual initial charge of the equipment should be conveyed clearly to the equipment user. If 

it is not, the user will underestimate emissions. The underestimate will occur because the user will underestimate 

the quantity of gas “purchased with or inside of equipment.” Effectively, an extra supply of gas is hidden inside the 

equipment rather than conveyed alongside it in a container. 

 

For example, suppose that a piece of equipment is charged to 105 percent of its proper charge (nameplate capacity) 

when it is first installed, but that its initial charge is recorded as 100 percent of the proper charge. Suppose further 

that the equipment slowly leaks over its lifetime so that it has 90 percent of its proper charge left upon retirement. 

When the equipment is retired, only the difference between the proper charge (100 percent) and the actual charge 

(90 percent) will be noticed. The loss of the extra five percent will not be recorded because the initial gain of that 

five percent was not recorded. In the event that the equipment never leaks during its lifetime and is retired with 105 

percent of its charge, the five-percent overcharge, when recovered along with the rest of the SF6 inside the 

equipment, will register as an addition to the SF6 in storage that is five percent above the retired nameplate capacity. 

Again, this will result in emissions being underestimated by the quantity of the overcharge. 

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To avoid the underestimate, equipment manufacturers should provide equipment users with an accurate estimate of 

the quantity of SF6 actually charged into newly commissioned equipment. The user would then record this as 

additional gas “purchased with or inside of equipment.” Using the standard mass-balance approach, this extra gas 

would register as an emission during the first year. This is because the extra gas would be recorded as part of the 

total amount of gas purchased during the year, but would not be canceled out by a corresponding increase to 

cylinder inventory (since the extra gas is inside the equipment) or by the increase to nameplate capacity (since the 

extra gas is by definition the amount of gas remaining once the nameplate capacity of the equipment is subtracted 

from the amount of gas actually inside the equipment). Since it would not be accounted for as an addition to 

inventory or as part of the new nameplate capacity, it would seem to have been emitted or used to replace emitted 

gas. However, this apparent loss would be made up for when the equipment was retired, as discussed above. 

 

An alternative approach to tracking the overcharge would be to record it as stored inside the particular piece(s) of 

equipment that is (are) overcharged. Effectively, this extra charge would be tracked as if it were stored inside a 

cylinder that happened to be attached to the equipment. The equipment would be checked annually to see whether 

and how much of its charge had leaked during the year; if the overcharge had not leaked out, then the overcharge 

would still be considered to be in storage and would not be recorded as an emission. Although this approach would 

avoid indicating an emission before any occurred, the need for annual checks of overcharged equipment would make 

it relatively burdensome to carry out. 

5. Review of Existing Relevant Reporting Programs/Methodologies 

In addition to the 2006 IPCC Guidelines, EPA also reviewed the protocols and guidance in the Inventory of U.S. 

Greenhouse Gas Emissions and Sinks, the Technical Guidelines for the Voluntary Reporting of Greenhouse Gases 

(1605(b)) Program, EPA’s Climate Leaders Program, and The Climate Registry. These protocols and guidance 

coalesce around the IPCC 2006 Tier 3 guidelines. 

6. Procedures for Estimating Missing Data 

It is expected that equipment manufacturers should be able to obtain 100 percent of the data needed to perform the 

mass balance calculations for both SF6 and PFCs. The use of the mass-balance approach requires correct records for 

all inputs. However, if needed, replace missing data using data from similar manufacturing operations, and from 

similar equipment testing and decommissioning activities for which data is available. 

 

7. QA/QC Requirements 

QA/QC methods for reviewing completeness and accuracy of reporting include the following: 

 Review inputs to the mass balance equation to ensure inputs and outputs to the manufacturer’s system are 

all accounted for in all appropriate sections. 

 Ensure no negative inputs are entered and negative emissions are not calculated. However, the change in 

storage inventory may be calculated as a negative number. 

 Ensure that beginning of year inventory matches end of year inventory from previous year. 

 Ensure that in addition to SF6 purchased from bulk gas distributors, SF6 returned from utilities and received 

from off-site recycling are properly accounted as additions to inventory. 

QA/QC methods should be employed throughout the year. Important checks/procedures include the following: 

 Ensure that cylinders returned to the vendor are weighed in a consistent manner. 

 Ensure that gas suppliers measure the amount of gas remaining in cylinders/tanks returned (residual gas). 

 Adopt practices such as tracking cylinders leaving and entering storage with check-out sheets and weigh-in 

procedures. 

 Ensure all facilities have provided information to the manager compiling the emissions report (if it is not 

already handled through an electronic inventory system). 

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8. Reporting Procedures 

The following supplemental data would aid in verifying facilities’ emissions estimates: 

 SF6 and PFC sales and purchases; 

 SF6 and PFCs sent off site for destruction; 

 SF6 and PFCs sent off site to be recycled; 

 SF6 and PFCs returned from off site after recycling; 

 SF6 and PFCs returned by equipment users with or inside equipment; 

 SF6 and PFCs stored in containers at the beginning and end of the year; 

 SF6 and PFCs inside equipment delivered to customers; 

 SF6 and PFCs returned to suppliers; 

 The nameplate capacity of the equipment delivered to customers with SF6 or PFCs inside, if different from 

the quantity in delivered to customers inside equipment; 

 A description of the engineering methods and calculations used to determine emissions from hoses or other 

flow lines that connect the container to the equipment that is being filled. 

 For any missing data, the reason the data were missing, the length of time the data were missing, the 

method used to estimate emissions in their absence, and the quantity of emissions thereby estimated. 

9. References 

EPA (2008) Inventory of U.S. Greenhouse Gas Emissions and Sinks: 1990-2006. U.S. Environmental Protection 

Agency, Washington, D.C. 

IPCC (2006) 2006 IPCC Guidelines for National Greenhouse Gas Inventories. The National Greenhouse Gas 

Inventories Programme, The Intergovernmental Panel on Climate Change, H.S. Eggleston, L. Buendia, K. Miwa, T 

Ngara, and K. Tanabe (eds.). Hayama, Kanagawa, Japan. 

MEPPI (2010) Personal Communication between Phil Bolin and Dave Giegel of Mitsubishi Electric Power 

Products, Inc. and Mollie Averyt of ICF International, February 24, 2010.

O’Connell, P., F. Heil, J. Henriot, G. Mauthe, H. Morrison, L. Neimeyer, M. Pittroff, R. Probst, J.P. Tailebois 

(2002) SF6 in the Electric Industry, Status 2000, Cigre. February 2002. 

RAND (2004) RAND Environmental Science and Policy Center, “Trends in SF6 Sales and End-Use Applications: 

1961-2003,” Katie D. Smythe. International Conference on SF6 and the Environment: Emission Reduction 

Strategies. Scottsdale, AZ. December 1-3, 2004. 

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