Appendix 1: Basis for Future Methodological Development

Appendix 1 (New) Possible Approaches for Estimating
Fluorinated Compounds Emissions from Textile, Carpet, Leather
and Paper Industries: Basis for Future Methodological
Development
1A.1

Introduction

Fluorine-based treatment of textiles for waterproofing was introduced in the 1950s (Davies 2014). The firstmicroporous membrane (polytetrafluoroethylene PTFE, also known as Teflon™) was created in 1969 and thefirst GORE-TEX™ materials appeared on the market in 1976 (Williams 2018). Since then, fluorochemicalfinishes have been widely used to functionalize fibres for water or oil repellence, soil and stain release,improving textile breathability, softening, dyeing ability, increasing mechanical strength, providing antibacterial
and anti-odour finishes, and for fabricating wrinkle-free materials (Choudhury 2017). Such applications arewidespread for the production of home textiles, upholstery furniture, protective clothing with signal colour, tent
canvas, outdoor wear, medical textiles and work wear such as uniforms and shoes (Lacasse & Baumann 2004;
Schindler & Hauser 2004; Singha 2012; Gulrajani 2013; Roshan 2014).
The conventional processes used for increasing the water repellence of fibres use perfluoroalkyl carboxylic acids(PFCAs) and perfluoroalkane sulfonic acids (PFSAs), commonly referred to as ‘C8’ chemistry because theprecursor molecules contain 8 carbon atoms. Such processes can lead to the formation of Perfluoroalkylated acidthrough oxidation, and in particular to the environmental release of perfluorooctane sulfonate (PFOS) andperfluorooctanoic acid (PFOA), two chemicals of concern due their persistent and bio-accumulative nature. As aresult, the use of C8 fluorinated polymers in textiles, carpet, leather, and paper has been restricted in someregions, and the industry is moving towards shorter chained chemistry (from ‘C8’ to ‘C6’ and ‘C4’). However,
the C6 and C4 chemistries have been reported to perform more poorly than the conventional C8 chemistry(Davies 2014), and the C8 chemistry continues to be widely used in regions with large textile production
capacities, particularly in developing countries (Fantke et al. 2015). Due to the lower performance of the shorter
chained chemistry, alternate methods are being sought for the treatment of textile, carpet, leather and paper. In
particular, plasma-based processes have shown promising performance (Davies 2014).
Fluorine-based plasma treatment of textile, carpet, leather, and paper has received increased interest and has
been a fertile subject for research and development (R&D) since the early 2000s, in part due to the fact thatplasma technologies provide excellent performance and that plasma processes can be tailored to achieve many
desirable properties. An increasing number of peer-reviewed papers have been published since 2006, and a
growing number of patents have been filed worldwide in the last 5 to 8 years, indicating that technological andindustrial developments are occurring rapidly in this emerging field. Several innovative treatment technologies
and chemistries are now transitioning to industrial scale use, particularly plasma processing of textiles using
gaseous fluorinated compounds (FC) such as CF4, C2F6, C3F8, C4F8, C5F10, CHF3, and SF6 (Yip et al. 2002;
Hochart et al. 2003; Raffaele-Addamo et al. 2003; Davis et al. 2011; Kwong et al. 2013; Ramamoorthy et al.
2013; Davies 2014; Zille et al. 2015; Saxena et al. 2017).
As in the case of the electronics sector, plasma-based processes using fluorinated compounds in the textile
industry are expected to result in emissions of unreacted fluorinated compounds and by-products with highglobal warming potentials (GWPs). However, the extent to which plasma processes have been introduced involume manufacturing is not clear. Also, the wet application of fluorinated surfactants and fluorine-based
polymers commonly used to treat textile, carpet, leather, and paper fibres can result in emissions of volatilefluorinated compounds through evaporative losses and cracking (IPPC 2003; OECD 2004). A list of the mostimportant fluorinated compounds used for plasma-based treatment processes is provided in Table 1Ap.1, and alist of the most important fluorotelomers, fluorocarbons, and fluorosurfactants used for wet applications, as wellas their vapour pressures, is provided in Table 1Ap.2. While the magnitude of FC emissions from the textile
industry as compared to other sources of fluorinated greenhouse gases (GHGs) is presently unknown, it is clearthat the textile industry contributes to some degree to the total amount of fluorinated substances found in theenvironment (KEMI 2014).
Although several international and national reports refer to the possible off-gas emissions of fluorinatedcompounds into the atmosphere due to textile treatment, no emission factors appear to be available in the open
literature to estimate greenhouse gas emissions from such processes (EPA 1997; Schönberger & Schäfer 2003;
MoEU 2012; DEPA 2013; UNIDO et al. 2017). Only one reference about emissions of hydro-fluorocarbons
related to the textile industry in the United Kingdom has be found in the literature (Ricardo-AEA 2015). As a

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consequence, the authors were not able – at the time of writing of this second order draft – to estimate thevolume of fluorinated compounds that are used or emitted by the textile, carpet, leather, and paper industries.
Nevertheless, FC emissions in this sector could represent a significant new source, due to the large volume ofsubstrates (i.e., product classes) treated and the sheer size and global nature of the industry.

1A.1.1

PLASMA TREATMENT PROCESSES

Plasmas are frequently subdivided into thermal (hot) and non-thermal (cold) plasmas. For thermal plasmas, thetemperature of electrons, ions, neutrals and excited species in the plasma state is in equilibrium, ranging from3,500 ºC to 20,000 ºC. Non-equilibrium (cold) plasmas have electron temperatures that are much higher than thetemperature of the ions and neutrals, where the temperature of the plasma is typically in the range of 40 to 250ºC. Because textiles and polymers cannot withstand the high temperatures used in thermal plasmas, mostapplications for organic fibres’ surface modification use cold plasmas. The majority of plasma-based textile
treatment processes for the production of hydrophobic and oleophobic surfaces (but also for some polymer coating,flame retardant and medical antimicrobial fabrics) reported in the technical literature are based on non-thermal
plasmas generated at low pressure (between 1 mTorr and 1 Torr) and in few cases at atmospheric pressure. Plasma
source designs based on corona discharges, glow discharges, dielectric barrier discharges (DBDs), plasma jet,capacitively or inductively coupled discharges, and RF- or microwave-induced discharges have been studied(Sigurdsson & Shishoo 1997; Tendero et al. 2006; Morent et al. 2008; Sparavigna 2008; Jafari et al. 2013; Vietro
et al. 2015; Zille et al. 2015; Gotoh et al. 2017).
Although most plasma processing technologies for textile treatments are still at an emerging stage, several
manufacturers have developed pilot- to commercial-scale machinery, and applications for specialized textiles
have been or are currently being implemented at industrial scale. Indeed, plasma treatment proves particularly
effective for the production of specialty textiles for the medical industry (gowns, masks, protective clothing), theautomotive industry (seats, trim, headliners, airbags), the apparel industry (outer and under garments), thefiltration industry (air, water filtration) and the flooring industry (carpet fibres) (Saxena et al. 2017). However,
the high capital and operational costs of plasma treatment (in particular for low-pressure plasma technologies
requiring a closed vacuum system) currently limits the commercial viability of the technique for treating
conventional (non-specialized) fabrics. Polymerization of textiles using plasma at atmospheric pressure offers alow-cost and environmentally-friendly alternative, but the technology is still under development (Shishoo 2007;
Muthu 2016).
Plasma processes used for the treatment of such materials can be divided into three process types: 1) plasma
treatment, 2) plasma etching (or ablation), and 3) plasma polymerization (Roth 2001).
1) Plasma treatment uses inert gases such as Ar, He, N2, and chemically active molecules such as O2 or
NH3, as well as fluorinated gases such as CF4, C2F6, C3F8, C4F8, C5F10, CHF3, SF6, and other (largersize) fluorine-containing molecules such as perfluoroalkyl acrylates (Tendero et al. 2006; Morent et al.
2008; Sparavigna 2008; Jafari et al. 2013; Yim et al. 2013; Vietro et al. 2015; Zille et al. 2015; Gotoh etal. 2017). Plasma treatments can be further separated into two processes sub-types: a) when the plasmaactivated gases introduce chemical functionalities or create and deposit free radicals onto the target
surface that can be subsequently used to cross-link or surface-graft other molecules to attain specificsurface properties (very often more hydrophilic surfaces); or b) when the fabric is first immersed in a
fluid of hydrophobic fluorinated pre-polymer with added initiators followed by a plasma treatment
leading to the grafting of the pre-polymer on the surface of the fabric.
2) Plasma etching is a process type where the substrate is bombarded with ions from the plasma. Three
process sub-types may be defined within the etching process type, depending on whether plasma is usedto a) clean, b) sterilize, or c) enhance surface adhesion of the fabrics. For example, dry plasma etching
can be accomplished by using CF4 in a plasma discharge to create active species capable of reacting
chemically with the layer to be etched (Sigurdsson & Shishoo 1997).
3) Plasma polymerization is a process type where a monomer in vapour phase such as CF4, C2F6, C3F6, orlarger fluorinated molecules such as fluorodecylacrylate is converted into reactive fragments to deposita thin film onto the substrate. Plasma polymerization can be further separated into two process subtypes: a) plasma-induced polymerization is when the polymerization process is a surface-based reaction
and, b) plasma-state polymerization is when fragments react in the gas phase to form larger moleculesthat are then deposited on the substrate (Morent et al. 2008).
For all process types and sub-types, it is highly improbable that all input chemicals are fully consumed in the process(IPCC 2006). Further, the plasma decomposition of input chemicals such as C2F6, C3F8, and larger chain fluorinatedmolecules is likely to result in the production of byproducts such as CF4, C2F6, CHF3 and other gases. Therefore,
plasma-based fluorinated treatment of textile, carpet, leather, or paper is expected to lead to emissions of FC
greenhouse gases. It should be noted that the potential for plasma-based polymerization processes to emit large

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Appendix 1: Basis for Future Methodological Development

amounts of FCs is likely lower than for the plasma treatment and plasma etching process types because, in thecase of polymerization, the input FC chemicals are meant to react and form solid byproducts on the substrate as
opposed to just treat or etch its surface. However, it should also be mentioned that plasma-based polymerization
is more effective than many conventional wet-based chemistries, and that such characteristics may contribute toshifting emissions towards high-GWP gases. Finally, the extent to which reactor cleaning processes (to remove
the deposits that build on the chamber walls after multiple depositions) may contribute to GHG emissions is
unclear at the time of writing of the Second Order Draft of the 2019 Refinement, and comments are sought on
this particular issue.

1A.1.2WET TREATMENT PROCESSES

Wet treatment processes include several application techniques but about 80per cent of the processes use thepad-dry-cure method, where the dry fabric is immersed in the finishing liquor and then squeezed between rollers
before being dried and finally cured, usually at a temperature of between 150 and 180 ºC (Roshan 2014). Other
techniques include vacuum extraction, spray applications, foam finishing, coating, and lamination.
Side-chain fluorinated polymers primarily based on fluorotelomer acrylates, fluorotelomer methacrylates or perfluoroalkane sulfonamidoethanols characterize the chemical structure of the fluorine-based surfactants andpolymers used for the above-described applications. Unfortunately, the environmental and health characteristics ofthe new short-chain chemistry and associated processes are poorly described in the scientific literature. Althoughsome reports refer to possible emissions of FCs in the atmosphere due to textile-wet coating, no data or estimationsof emissions are provided (IPPC 2003; Ellis et al. 2004; OECD 2004; Dumoulin et al. 2005; Prevedouros et al.
2006; Barber et al. 2007; Jahnke et al. 2007; FOEN 2009; Young 2010; DEPA 2015; UNEP 2017). Data on thevolatile PFASs that are emitted immediately after the production of textiles, the type of PFASs that can be formedby hydrolysis of the perfluorinated polymer side chains during use, washing and degradation of the fabrics is alsoseemingly missing.
Importantly, it must be considered that FC products are likely to be released to the air during their industrial
application to fibres, particularly during the curing phase of the treatment. It has been shown that, during thedrying and curing phases, off-gas emissions can be produced by the volatility of the active substances themselves
as well as by their constituents, which can contain on average 1per cent of unreacted and unbound residuals suchas monomers, fluorotelomer alcohols (sometimes up to 6-8per cent of the dry weight) and perfluoroalkyl
carboxylic acids (Heydebreck et al. 2016). Overall, it can be expected that the magnitude of emissions will
depend on the drying or curing temperature, the substrate material, and the reagents’ volatility, concentrations
and reactivity (European Commission 2003). To complicate the matter, there is a wide range of different
application methods (e.g. padding, spray, foaming, coating, lamination, etc.), different vapour pressure of input
chemicals, and different temperature and time of drying and curing steps of the treated substrates. For example,
some leather stain resistant finishing agents are applied by spray and dried at room temperature while most of the
textile finishing require a drying (110-130ºC) and curing (150-180 ºC) steps (Williams 2018). Carpet products
may be cured at a lower temperature of 110 ºC while other products may be treated for 2 minutes at 170ºC or for
30 seconds at 190ºC (e.g. cotton). Moreover, some carpet treatments require a curing step for water and oil
repellence when using FCs deposition, but on the contrary no curing is required for some type of solvent soluble
fluorinated soil release finishing agents for garments, upholstery and carpets (Goswami 2017). However, thelatter kind of treatments has lower durability than water-based FCs because of the lack of fixation bycrosslinking (Schindler & Hauser 2004). Generally, the higher the curing temperature, the shorter is the curing
time in order to avoid yellowing of the fabric. Residuals and impurities may also be released directly from theproducts into the environment through volatilization, and FC emissions may result from the cracking of input
chemicals. Thus, presumptively, emissions of high-GWP gases from wet-based fluorinated treatment of textile,leather, and paper fibres may represent a substantial source. However, the potential climate impact of suchprocesses and substances does not appear to have been characterized in the literature, which typically focuses onformaldehyde, total organic carbon release and on a very limited selection of well-known long-chain PFASs
such as perfluorooctanesulfonate (PFOS), perfluorooctanoic acid (PFOA) and their precursors (Wang et al.
2017).

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TABLE 1AP.1
LIST OF MOST IMPORTANT INPUT CHEMICAL MONOMERS USED IN PLASMA TREATMENT OF TEXTILES
Atmospheric plasma1

Low pressure plasma2

C11H7F13O2
C13H7F17O2/C15H7F21O2
Unidyne TG-571®
CF4 (PFC-14)
CHF2CF3 (HFC-125)
CHF3 (HFC-23)
C3F6 (Perfluorocyclopropane)
C2F6 (PFC-116)
C8F17CH2CH2OCOCH=CH2
C3F8 (PFC-218)
C13H7F17O2
SF6 (Sulfur hexafluoride)
H2C=CHCO2CH2CH2(CF2)7CF3
C6H13F3O3Si (FAS-3)
C6F5Si(OC2H5)3 (FAS-5)
C13H13F17O3Si (FAS-17)

CF4 (PFC-14)
C2F4 (PFC-1114)
C3F6 (Perfluorocyclopropane)
C2F6 (PFC-116)
C3F8 (PFC-218)
C4F10 (PFC-31-10)
C6F14 (PFC-51-14)
C4F8 (PFC-318)
CHF2CF3 (HFC-125)
SF6 (Sulfur hexafluoride)
CF3SO3H (co-monomer)
C2ClF3 (co-monomer)
C6F6 (co-monomer)
HC6F5 (co-monomer)
CF3(CF2)7CH=CH2
1,1,2,2, tetrahydroperfluorodecyl acrylate (AC8)Note:
Despite the fact that some chemicals have been defined using their common names, most of the listed chemicals represent chemicalfamilies, co-monomers or commercial products. Please refer to the IUPAC name for the other chemicals.
Sources:1
Yim et al. 2013; Gotoh et al. 2017; Tendero et al. 2006; Zille et al. 2015; Sparavigna 2008; Morent et al. 2008
2
Vietro et al. 2015; Zille et al. 2015; Sparavigna 2008; Morent et al. 2008; Jafari et al. 2013; Hochart et al. 2003; Hegemann 2006

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TABLE 1AP.2
LIST OF MOST IMPORTANT INPUT CHEMICALS USED IN WET TREATMENT PROCESS, AND THEIR VAPOUR PRESSURE
Vapour pressure (mm Hg @ 25°C)1

Chemical name
Tetrafluoroethylene
Chlorotrifluoroethylene
Vinylidene fluoride
Vinyl fluoride
Hexafluoropropene
Perfluoromethylvinyl ether
Perfluoropropylvinyl ether
Perfluorooctane sulfonic acid (PFOS)
Perfluorobutane sulfonic acid (PFBS)
n-methyl perfluorobutane sulfonamidoethanol (Me-FBSE)
3-(Perfluorobutyl)propanol (PFBP)
Ethyl perfluorooctanoate (EPFO)
Perfluoro-3,6-dioxaheptanoic acid (PDHA)
Fluorotelomer alcohol 10:2 FTOHPFOA isomers
Perfluorooctane sulfonyl fluoride (POSF)
Fluorotelomer alcohol 8:2 FTOH
Perfluorohexanoic acid (PFHxA)
Heptafluorobutyric acid - C4HF7O (PFBA)
Perfluorobutanoic acid (PFBA)
Fluorotelomer alcohol 4:2 FTOH
1,1,2,2-Tetrafluoroethyl methyl ether
Perfluorobutyl iodide
Polyfluorinated fluorotelomer iodides (6:2 FTI)
C6F14 (PFC-51-14)
C5F11NO
C8F18(perfluorooctyl)ethylene (PFOE)1(Perfluorohexyl)ethylene
1H,1H,2H-Perfluoro-1-decene
Fluorotelomer alcohol 6:2 FTOH
C5F12 (PFC-41-12)
C7F16

24500
4590
30000
19800
4900
765
534
0.002
0.027
0.05
0.7
0.97-11.06
1.1 - 0.001
1.26 - 2.04
5.75
1.9 - 0.03
1.98
1010 (20ºC)
12.5 - 1.6
1280
158
2.9
232
274
29
3.6
43.8
6.36
6.6 - 0.1
610
79

Notes:- Please note that even though most of the PFOS and PFOA compounds have very low vapour pressure at 25 ºC, they are cured during
applications at temperatures of between 150 and 180 ºC.
- Despite the fact that some chemicals have been defined using their common names most of the listed chemicals represent chemicalfamilies. Please refer to the IUPAC name for the other chemicals.
Sources:1
Schindler et al. 2013; National Institutes of Health; Nielsen 2012; Ruan et al. 2013; Harrad 2001

1A.2

Methodological issues

1A.2.1CHOICE OF METHOD

The choice of method will eventually depend on the availability of measured emission factors from which
default factors might be derived. The bibliographic research conducted as of the date of this Second Order Draft
does not indicate that representative FC emissions data can be obtained from the textile, carpet, leather, or paperindustries to derive default emission factors for Tier 1 or Tier 2 methods. Nevertheless, the authors propose
herewith a four-tiered methodological framework (Tier 1, Tier 2a, Tier 2b, and Tier 3) to account for emissions
from this sector. At this point, because no Tier 1 or Tier 2 default factors are available, only the Tier 3 method ispracticable, using equipment-specific, process-specific, or site-specific measured emission factors. Distinct
methods are provided for plasma-based processes and for wet-based processes. This Appendix provides a basis
for future methodological development rather than complete guidance.
The inventory methods proposed for plasma-based processes are analogous to those used in the electronics
industry due to the similarity of the processes, and include four tiered methods (Tier 1, 2a, 2b, 3). The Tier 1
method does not require gas consumption data and provides an estimate of emissions based on default (industry
average) emission factors expressed in mass of FC emitted per unit area of substrate treated. The Tier 2a and 2b
methods require FC consumption data at the site or national level and are based on process gas-specific default

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Volume 3: Industrial Processes and Product Useemission factors expressed in terms of mass of FC emitted per mass of FC consumed (including both emissionsof unreacted FC and emissions of all FC by-products formed during the process). For plasma processes, thedifference between the Tier 2a and 2b methods is that the Tier 2b method differentiates emission factors by typeof plasma process (plasma treatment, plasma etching, and plasma polymerization) and/or class of products
manufactured (textiles, leather, paper, etc.), while the Tier 2a method does not. A Tier 3 method would use thesame equations as the Tier 2b method, but would use measured emission factors (equipment-specific, processspecific, substrate-specific, or site-specific) instead of default emission factors.
For wet-based processes, a Tier 1 approach is proposed as a framework to estimate FC emissions based on themass of substrate treated, a method, which would therefore not require data on the consumption of input
chemicals. Two Tier 2 methods (Tier 2a and 2b) are also proposed as frameworks to report emissions based on
default FC emission factors allowing to correlate the mass of wet input chemicals consumed to the mass ofvolatile by-products formed during the processes. The difference between the Tier 2a and 2b methods for wet
processes is that the Tier 2b method would distinguish emission factors by process and/or substrate type (class of
products) (see further discussion below), while the Tier 2a method would not. Finally, a Tier 3 method
applicable to wet processes would use the same equations as the Tier 2b method, but would use measured
emission factors (equipment-specific, process-specific, or site-specific) instead of default emission factors.
Generally, the higher tiered methods will be more accurate than the lowered tiered ones, and using equipmentspecific, process-specific, or site-specific emission factors will improve accuracy and greatly reduce theuncertainty of emissions estimates. The accuracy of the methods using default emission factors depends, interalia, on the differences between the emission factors of the processes actually used in production and theaveraged (default) emission factors of a particular method, as well as on potential errors in allocating theconsumption of input chemicals, and in reporting the abatement efficiency and the uptime of emissions control
systems. With respect to uncertainty, the confidence level of a particular emissions estimate will likely be
principally driven by the uncertainty of the default emission factors.

1A.2.1.1

PLASMA TREATMENT PROCESSES

Table 1Ap.3 depicts the information sources necessary for completing the tiered methods for estimating
emissions from plasma treatment processes. This information is preliminary and likely to evolve as thedefinitions of the various methods are refined. At the time of writing of this Second Order Draft, no information
about emission factors could be obtained for plasma treatments from the textile, carpet, leather, or paperindustries to derive default emission factors for the Tier 1, Tier 2a, or Tier 2b methods. Thus, currently, the only
practicable means to estimate emissions from this sector is the use of the Tier 3 method. Nevertheless, when astatistically-significant number of representative experimental emission factors becomes available, preliminary
recommendations are provided for estimating default emission factors and for choosing the most appropriate
Tier 1, Tier 2a, or Tier 2b methods.
Depending on the method used, data based on production capacity (Tier 1), or data about input chemicals
consumption, use rate, by-products formation rates, and the effectiveness of emissions control measures (Tier 2a,2b, 3) will be required for the calculation of emissions. For each variable, depending on the tiered method, an
industry default value (D) may be used, measured (Me), or modelled (Mo) to account for site-specific values.
With respect to accounting for emissions control technologies, the approach provided here is analogous to themethod provided for the electronics industry. For more information, please refer to Chapter 6 “Electronic
Industry Emissions”.
While continuous (in-situ) emissions monitoring may be technically feasible, it is unclear whether such an
approach could be an economically viable method to estimate emissions from the textile, carpet, leather, or paperindustry. One alternate approach would be to measure emission factors during the development of new plasma
processes when parameters such as input gas flows, chamber pressure, processing time, plasma power, etc. areadjusted for particular treatment needs or for manufacturing a particular product. Please see Box 1Ap.1 for
guidance on the analytical methods that can be used for measuring emission factors.
Another approach would be for facilities to periodically (for short periods of time) install equipment to measureemissions from their stacks for purposes of developing facility-specific emission factors to estimate emissions
over the long term (see, e.g., the Tier 3b method developed for Chapter 6 “Electronic Industry Emissions”). It isvery important to note that emission factors (i.e. input gas utilization efficiencies and by-product formation rates)
can be strongly affected by changes in process variables (e.g. type of textile substrate material, pressure,temperature, plasma power, FC gas flow, processing time, etc.) and by the design of the process reactors. Thus,
emission factors can substantially fluctuate from one tool manufacturer to another and for a recipe ‘tuned’ for aparticular purpose or product.

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TABLE 1AP.3
INFORMATION SOURCES NECESSARY FOR COMPLETING THE TIERED EMISSIONS ESTIMATING METHODS FOR PLASMATREATMENT OF TEXTILE, LEATHER, AND PAPER
Tier 1

Tier 2Tier 3

Data

Process Gas Reactions andConversion in Tools

Process Gas Entering
Tools

2a
FCi, = consumption of gas i

Me/Mo

FCi,p = consumption of gas i for process p.a
hi = Fraction of gas remaining in shipping container
after use (heel) for gas i.

D/Me

Ui = Use rate (fraction destroyed or transformed) for
each gas i.

DUi,p = Use rate (fraction destroyed or transformed)
for each gas i and process p.a
Bk,i, = Emission factor for by-product k for input gas
i.

Downstream FC Emission Control

ai, = Fraction of gas i volume used in processes withcertified FC emission control technology

Me/Mo

D/Me

Me

D

Me

D

Me

Mea

Mea

D/Mea

D/Mea

Mea

Mea

Me

ai,p, = Fraction of gas i volume fed into processes p
with certified FC emission control technology
di = Destruction Removal Efficiency (DRE) for gas i

D/Medi,p = Destruction Removal Efficiency (DRE) for gas
i for process p
UT = Average uptime factor of all abatement
systems connected to process tools

Me

UTp = Average uptime factor of all abatement
systems connected to process tools running process
type pAnnual Production
Capacity

Me/Mo

D

Bk,i,p = Emission factor for by-product k for input
gas i and process p.a

EFi = emission factor for FC gas iD

Cu = fraction of annual plant production capacity
utilizationMe

Cd = annual manufacturing design capacity

2b

Me

Me = measurement; Mo = model {modelling criteria TBD}; D = Use default factors from guidance.
aDepending on the method used, ‘p’ is to be interpreted as a particular plasma process type (Tier 2b) or a site-specific process (Tier 3).

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TIER 1 METHOD FOR PLASMA TREATMENT PROCESSES – DEFAULTThe Tier 1 method is the least accurate estimation method and should be used only in cases where site-specificdata on the consumption of input chemicals are not available. The Tier 1 method, unlike the Tier 2a, 2b or Tier 3
methods, is designed to give an aggregated estimate of FC emissions, although its methodology appears to
produce gas-specific emissions. As envisioned, Tier 1 estimates would be made simultaneously for all (or for themost important) gases listed in Table 1Ap.1 and could only be used if reported as a complete set.
As proposed, the Tier 1 calculation relies on a fixed set of generic emissions factors and does not account fordifferences among process types (plasma treatment, etching, or polymerization), individual processes or
manufacturing tools. However, the members of the set would likely differ depending on the surface area oftextile, carpet, leather, or paper products being manufactured. Each member of a set, which is a gas-specificemission factor, would express average emissions per unit of substrate area (textile, carpet, leather, paper)produced during manufacture.
In using Tier 1, inventory compilers should not modify, in any way, the set of FCs assumed to represent average
emissions. Further, as is common practice for IPCC methods, the Tier 1 method does not allow accounting for theuse of emissions control technologies, and inventory compilers should not combine emissions estimated using
Tier 1 method with emissions estimated using the Tier 2 or 3 methods. Neither may inventory compilers use, forexample, the Tier 1 factor for CF4 to estimate the emissions of CF4 from textiles etching and combine it with theresults of other FC gases from a Tier 2 or Tier 3 method. The formula used to calculate Tier 1 emissions isshown in Equation 1Ap.1.

EQUATION 1AP.1
TIER 1 METHOD FOR ESTIMATION OF THE SET OF FC EMISSIONS{FCi }n= {EFi • Cu • Cd }n(i= 1,..., n)

Where:{𝐹𝐹𝐹𝐹𝑖𝑖 }𝑛𝑛 = emissions of FC gas i, mass of gas iNote: { }n denotes the set for each class of products (e.g. textile, carpet, leather, or paper) and n denotes
the number of gases included in each set. The estimates are only valid if made and reported for all
members of the set using this Tier 1 methodology.
𝐸𝐸𝐸𝐸𝑖𝑖
𝐶𝐶𝑢𝑢
𝐶𝐶𝑑𝑑= FC emission factor for gas i expressed as annual mass of emissions per square meters of
substrate surface area for the product class, (mass of gas i)/m2= fraction of annual plant production capacity utilization, fraction= annual manufacturing design capacity, m2 of substrate processed

TIER 2A METHOD FOR PLASMA TREATMENT PROCESSES – PROCESSCHEMICAL-SPECIFIC PARAMETERS
The Tier 2a method uses industry-wide default values for the fraction of input chemicals used in the plasma
manufacturing process (Ui), the fraction of input chemicals i converted into FC by-products k during the process(Bk,i), and the fraction of FC destroyed by the emissions control technology (Di). The Tier 2a method also
calculates emissions for each input chemical used on the basis of site-specific data on chemicals consumption
and emissions control technologies. Thus, to use the Tier 2a method, inventory compilers must have directcommunication with industry (e.g., annual emissions reporting) to gather consumption data and ensure thatemission control technologies are installed and used in accordance with the guidelines provided in thisdocument. For the ‘heel’ or fraction of the purchased gas remaining in the shipping container after use (hi),facilities may use default or site-specific values. 1
Unlike the Tier 2b and Tier 3 methods that are explained later in this section, the Tier 2a method does notdistinguish between process types (treatment, etching, or polymerization) or site-specific processes. However,

1 For an example of how site-specific heel factors can be developed, please see Chapter 6 Volume 3 of the 2019 Refinement.

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Appendix 1: Basis for Future Methodological Development

the Tier 2a default emission factors are formed separately for each input chemical, which, unlike the Tier 1
method, allows to account for the actual mix of input chemicals used at a particular manufacturing site.
Total Tier 2a emissions are equal to the sum of emissions from all unreacted fluorinated chemicals i used in the
production process (Ei) plus emissions of all by-products k (BPEk) resulting from the conversion of all input
chemicals used during production, as calculated using equations 1Ap.2, and 1Ap.3 below.

EQUATION 1AP.2
TIER 2A ESTIMATION OF EMISSIONS OF UNREACTED INPUT CHEMICALSEi = (1 − hi ) • FCi • (1 − U i ) • (1 − Di )Where:𝐸𝐸𝑖𝑖 = emissions of unreacted input chemical i, kgℎ𝑖𝑖 = fraction of input gas i remaining in shipping container (heel) after use, fraction
𝐹𝐹𝐹𝐹𝑖𝑖 = consumption of input chemical i, kg

𝑈𝑈𝑖𝑖 = use rate of input chemical i (fraction destroyed or transformed in process), fraction

𝐷𝐷𝑖𝑖 = Overall reduction of gas i emissions, fraction, calculated per equation 1Ap.4
EQUATION 1AP.3
TIER 2A ESTIMATION OF BY-PRODUCT EMISSIONS

BRE=k∑ (1 − h ) • B • FC • (1 − D )
i

i

k, i

i

k

Where:𝐵𝐵𝐵𝐵𝐵𝐵𝑘𝑘 = emissions of by-product k generated from the conversion of all input chemicals i, kgℎ𝑖𝑖= fraction of input gas i remaining in shipping container (heel) after use, fraction

𝐹𝐹𝐹𝐹𝑖𝑖= consumption of input chemical i, kg

𝐷𝐷𝑘𝑘= overall reduction of gas k by-product emissions, fraction, calculated per equation 1Ap.4(replacing i by k indexes)

𝐵𝐵𝑘𝑘,𝑖𝑖 = emission factor, kg of by-product k created per kg of input chemical i used

EQUATION 1AP.4
EMISSIONS REDUCTION IMPACT OF EMISSIONS CONTROL TECHNOLOGY

Di = ai • di • UT
Where:
𝐷𝐷𝑖𝑖 = overall reduction of chemical i emissions, fraction

𝑎𝑎𝑖𝑖 = fraction of chemical i volume used in processes with emission control technologies (site-specific),
fraction

𝑑𝑑𝑖𝑖 = Destruction Removal Efficiency (DRE) for chemical i, fraction

𝑈𝑈𝑈𝑈 = average uptime of all abatement systems, fraction, calculated per Equation 1Ap.5

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EQUATION 1AP.5
UPTIME OF EMISSION CONTROL SYSTEMUT = 1 −

∑ Td
∑ UT
n

n

n

n

Where:𝑈𝑈𝑈𝑈 = average uptime factor of all abatement systems connected to process tools, fraction

𝑇𝑇𝑇𝑇𝑛𝑛 = The total time, in minutes, that abatement system n connected to process tool(s) in the plant, is not
in operational mode when at least one of the manufacturing tools connected to abatement system n is
in operation
𝑈𝑈𝑈𝑈𝑛𝑛 = total time, in minutes per year, in which abatement system n has at least one associatedmanufacturing tool in operation. UT may be set to 1 if suitable backup abatement or interlocking
with the process tool is implemented for each abatement system 2n= abatement system

TIER 2B METHOD FOR PLASMA TREATMENT PROCESSES – PROCESSTYPE-SPECIFIC PARAMETERS
The Tier 2b method is similar to the Tier 2a approach in the sense that it is based on chemical-specific default
emission factors, but the Tier 2b factors also account for the type of plasma process and/or class of products (i.e.
textile, carpet, leather, paper) used for production processes ‘p’. Thus, the Tier 2b approach is expected to be
more accurate than the Tier 2a one because the Tier 2b method reflects the mix of processes or classes of
products used in a particular manufacturing facility. Also, the Tier 2b method allows to account for the trend
where some chemicals tend to be used predominantly in particular process types and class of products
manufactured. The Tier 2b method uses industry-wide default values for the fraction of input chemicals i used inplasma production process p (Ui,p), the fraction of input chemicals i converted into FC by-products k during
process p (Bk,i,p), and the fraction of FC destroyed by the emissions control technology connected to tools using
production process p (Di,p). For the ‘heel’ or fraction of the purchased gas remaining in the shipping container
after use (hi), facilities may use default or site-specific values. 3
Although the Tier 2b method is preferred over the Tier 2a method because process- or product-type specificemission factors are more accurate, it should be noted that the Tier 2b method presents increased complexity
because the consumption of input chemicals must be allocated to each production process p. Thus, in the casewhere the consumption of input chemicals cannot directly be measured for each production process p, a gas
consumption allocation model must be devised for applying the method, 4 and inventory compilers should
consider the trade-off of using more accurate process-specific emission factors versus introducing errors in the
Tier 2b estimate, due to uncertainties in the allocation model.
Total Tier 2b emissions are equal to the sum of emissions from all unreacted fluorinated chemicals i used in all
production processes p (Ei) plus emissions of all by-products k resulting from the conversion of all input
chemicals used during all production processes p (BPEk), as calculated using equations 1AP.6, and 1AP.7 below.

2 For determining the amount of tool operating time, you may assume that tools that were installed for the whole of the year

were operated for 525,600 minutes per year. For tools that were installed or uninstalled during the year, you should prorate
the operating time to account for the days in which the tool was not installed; treat any partial day that a tool was installed
as a full day (1,440 minutes) of tool operation. For an abatement system that has more than one connected tool, the tool
operating time is 525,600 minutes per year if at least one tool was installed at all times throughout the year. If you havetools that are idle with no gas flow through the tool for part of the year, you may calculate total tool time using the actual
time that gas is flowing through the tool.
3 For an example of how site-specific heel factors can be developed, please see Chapter 6 Volume 3 of the 2019 Refinement.
4 For an example of how site-specific gas consumption allocation models can be developed, please see Chapter 6 Volume 3of the 2019 Refinement.

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EQUATION 1AP.6
TIER 2B ESTIMATION OF EMISSIONS OF UNREACTED INPUT CHEMICALSEi = (1 − hi ) • ∑ p  FCi , p • (1 − U i , p ) • (1 − Di , p ) 
Where:
𝐸𝐸𝑖𝑖ℎ𝑖𝑖= emissions of unreacted input chemical i, kg= fraction of input gas i remaining in shipping container (heel) after use, fraction

𝐹𝐹𝐹𝐹𝑖𝑖,𝑝𝑝 = consumption of input chemical i for production process p, kg

𝑈𝑈𝑖𝑖,𝑝𝑝 = use rate of input chemical i (fraction destroyed or transformed in production process p), fraction

𝐷𝐷𝑖𝑖,𝑝𝑝 = overall reduction of gas i emissions from tools using production process p, fraction, calculated per
equation 1Ap.8
EQUATION 1AP.7
TIER 2B ESTIMATION OF BY-PRODUCT EMISSIONS

BPE
=
k

∑ (1 − h ) • ∑  Biipk , i, p• FCi , p • (1 − Dk , p )  

Where:𝐵𝐵𝐵𝐵𝐵𝐵𝑘𝑘 = emissions of by-product k generated from the conversion of all input chemicals i used for allprocess types p, kgℎ𝑖𝑖= fraction of input gas i remaining in shipping container (heel) after use, fraction

𝐵𝐵𝑘𝑘,𝑖𝑖,𝑝𝑝 = emission factor, kg of by-product k created per kg of input chemical i used for production processp

𝐹𝐹𝐹𝐹𝑖𝑖,𝑝𝑝 = consumption of input chemical i for production process p, kg

𝐷𝐷𝑘𝑘,𝑝𝑝 = overall reduction of gas k by-product emissions from tools using production process p, fraction,
calculated per equation 1Ap.8 (replacing i by k indexes)
EQUATION 1AP.8
EMISSIONS REDUCTION IMPACT OF EMISSIONS CONTROL TECHNOLOGY

Di , p = ai , p • di , p • UTp
Where:
𝐷𝐷𝑖𝑖,𝑝𝑝 = overall reduction of chemical i emissions from production process p, fraction𝑎𝑎𝑖𝑖,𝑝𝑝 = fraction of chemical i volume fed into production process p with emission control technologies(site-specific), fraction
𝑑𝑑𝑖𝑖,𝑝𝑝 = Destruction Removal Efficiency (DRE) for chemical i and production process p, fraction

𝑈𝑈𝑈𝑈𝑝𝑝 = average uptime of all abatement systems connected to tools using production process p, fraction,
calculated per Equation 1Ap.9

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EQUATION 1AP.9
UPTIME OF EMISSION CONTROL SYSTEMSUTp = 1 −

∑ Td
∑ UT
n

n, p

n

n, p

Where:𝑈𝑈𝑈𝑈𝑝𝑝= average uptime factor of all abatement systems connected to process tools running production
process p, fraction

𝑇𝑇𝑇𝑇𝑛𝑛,𝑝𝑝 = The total time, in minutes, that abatement system n connected to process tool(s) running
production process p in the plant, is not in operational mode when at least one of the
manufacturing tools connected to abatement system n is in operation
𝑈𝑈𝑈𝑈𝑛𝑛,𝑝𝑝 = total time, in minutes per year, in which abatement system n has at least one associatedmanufacturing tool running production process p in operation. UT may be set to 1 if suitablebackup abatement or interlocking with the process tool is implemented for each abatement
system 5n= abatement system

TIER 3 METHOD FOR PLASMA TREATMENT PROCESSES – SITESPECIFIC PARAMETERS
The Tier 3 method uses the same set of equations (equations 1Ap.6 to 1Ap.9) as the Tier 2b method. However,when using the Tier 3 method, inventory compilers need to interpret ‘p’ in these equations as a specificproduction process using a specific ‘recipe’. A recipe corresponds to a particular combination of input gases
under specific conditions of process duration, temperature, pressure, flow, plasma power, class or product, andother relevant process parameters adjusted to achieve a particular result (i.e. water or stain resistance, increased
mechanical strength, etching medical polyamide, etc.) on a specific process reactor. It is very important to notethat emission factors such as input gas utilisation efficiencies and by-product formation rates can be strongly
affected by changes in process parameters (duration, temperature, pressure, flow, plasma power, reactor design,etc.).
When using the Tier 3 method, the (1-U) and BPE emission factors in Equations 1.Ap.6 and 1.Ap.7 should bemeasured for specific processes recipes. However, a centreline process recipe may be used to establish Tier 3
emission factors for sets of ‘similar’ recipes. Recipes can be deemed ‘similar’ when the centreline process canreasonably be deemed representative of facility-specific process conditions, of the potential variability of suchprocess conditions around the centreline process during normal manufacturing operations, and when the process
type (plasma treatment, plasma etching, and plasma polymerization), product, process tool, and input processgases are the same. When using the concept of ‘similarity’, inventory compilers should be able to reasonably
demonstrate that emissions estimates are not biased (i.e. systematically over- or under-estimated) when using
centreline process recipe(s) emission factors.
Once default Tier 2a or Tier 2b emission factors will be developed, the Tier 3 method should be used bymanufacturing plants whose processes and recipes depart significantly from industry-wide patterns of use (e.g.
for facilities using an input chemical primarily in plasma etching while others primarily use it in plasma
polymerization), or by manufacturing plants that may have developed specific processes whose characteristics
may result in a significantly lower or higher utilization of input chemicals or formation of byproducts. Further, if

5 For determining the amount of tool operating time, you may assume that tools that were installed for the whole of the year

were operated for 525,600 minutes per year. For tools that were installed or uninstalled during the year, you should prorate
the operating time to account for the days in which the tool was not installed; treat any partial day that a tool was installed
as a full day (1,440 minutes) of tool operation. For an abatement system that has more than one connected tool, the tool
operating time is 525,600 minutes per year if at least one tool was installed at all times throughout the year. If you havetools that are idle with no gas flow through the tool for part of the year, you may calculate total tool time using the actual
time that gas is flowing through the tool.

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default Tier 2 emission factors are not available for a particular process or input chemical, manufacturing
facilities should measure their site-specific emission factors and use the Tier 3 method.
It should also be noted that Tier 3 emission factors could be combined with Tier 2a or 2b default emission
factors (once available) to use a hybrid method. A hybrid method would involve applying the Tier 2 defaults toprocesses and technologies that have not changed while applying Tier 3a, site-specific emission factors toprocesses and technologies that have changed. Indeed, higher accuracy might be achieved by using the Tier 3
method for specific input chemicals or site-specific processes. However, inventory compilers should not
combine the Tier 1 method with any other method.
The Tier 3 method is not outlined further in this Appendix, but inventory compilers should refer to the Box
1Ap.1 on specific technologies for the measurement of FC emissions in order to develop facility- or countryspecific emission factors as a resource for implementing the Tier 3 method. Also, measurement methods
developed for the electronics industry could be used as a basis for measuring emission factors from plasmabased finishing processes in the textile, carpet, leather, and paper industries (Benaway et al. 2014).

BOX 1AP.1
ANALYTICAL METHODS FOR MEASURING FC EMISSIONS

Fourier transform infrared spectroscopy (FTIR) is the currently preferred option due to part perbillion (ppb) sensitivity, portability, ability to enable near-real-time measurements, reprocess
historical data, and provide multi-component analysis and resistance to magnetic fields. However,FTIRs are generally considered to be higher-cost systems, requiring significant upkeep during
sampling campaigns. Depending on the absorptivity and concentration of the FC gases to be
detected, FTIR gas cells with long path lengths (meters) might be required to reach suitabledetection levels (Espinoza-Nava et al. 2016).
Gas chromatography followed by mass spectrometry (GC/MS) can provide a near real timemeasurement of FC, as well as several other gas sample components if desired. The instrument
must be calibrated in place, prior to the start of FC monitoring. If GC/MS measurement is notpossible on a continuous basis this technology allows for sample collection that can be transported
to a laboratory for analysis, directly in sample bags or by desorbing components after time average
sampling onto sorbent columns. Using samples in bags or metal canisters, detection limits of 0.05
ppmv and 0.04 ppmv for CF4 and C2F6, respectively, can be achieved. Using the sorbent columns
detection limits of 9 ppbv for CF4 and 0.6 ppbv for C2F6 have been validated (EPA & IAI 2008).
Detection limits can be improved with modification of desorption parameters if desired. Method
Detection Limit (MDL) from 0.001 to 3.5 pg.m-3 were reported for indoor and outdoor
determination of several volatile perfluorinated compounds with the use of high volume samples
and efficient enrichment steps (Trojanowicz & Koc 2013).

1A.2.1.2

W ET TREATMENT PROCESSES

Table 1Ap.4 depicts the information sources necessary for completing the tiered methods for estimating
emissions from wet-based treatment of textiles, carpet, leather, and paper. This information is preliminary andlikely to evolve, as the definitions of the various methods are refined. At the time of writing of this Second Order
Draft, no information about emission factors could be obtained for wet-based treatments from the textile, carpet,
leather, or paper industries to derive default emission factors for the Tier 1, Tier 2a, or Tier 2b methods. Thus,
currently, the only practicable means to estimate emissions from this sector is the use of the Tier 3 method.
Nevertheless, when a statistically-significant number of representative experimental emission factors become
available, preliminary recommendations are provided for estimating default emission factors and for choosing
the most appropriate Tier 1, Tier 2a, or Tier 2b methods.
Depending on the method used, data based on production capacity (Tier 1), or data about input chemicals
consumption, use rate, by-products formation rates, and the effectiveness of emissions control measures (Tier 2a,2b, 3) will be required for the calculation of emissions. For each variable, depending on the method, an industry
default value (D) may be used, modelled (Mo), or measured (Me) to account for site-specific values. As
mentioned earlier, emissions of greenhouse gases from wet treatment processes may result from evaporative
losses of the input liquid chemicals and from the formation of volatile fluorinated compounds through chemical
reactions during the processes, all of which can be considered volatile by-product emissions resulting from theuse of the liquid input chemicals. Thus, unlike for plasma-based processes, the equations for the Tier 2a, 2b and2019 Refinement to the 2006 IPCC Guidelines for National Greenhouse Gas Inventories

Ap1.13Volume 3: Industrial Processes and Product Use

Tier 3 methods for wet treatment processes do not take into account the utilization efficiency of the input liquid
chemicals – most of which remain on the substrate as a coating (in a solid state), and only volatile by-productemission factors are necessary to account for all emissions (EVi and Bk,i for the Tier 2a and EVi,p and Bk,i,p for the
Tier 2b and Tier 3 methods). Also, the equations for wet treatment processes do not include a heel factor(fraction of gas remaining in the shipping container in the methods used for plasma-based processes). The
emission factors for textile industry will be calculated for the emission potential of auxiliaries to the produced
amount of textile in kg. 6
While continuous (in-situ) emissions monitoring may be technically feasible, it is unclear whether such approach
could be an economically viable method to estimate emissions from the textile, carpet, leather, or paper industry.
One alternate approach would be to measure emission factors during the development of new wet-based
processes when parameters such as coating velocity, liquid ratio, processing time, curing and dying
temperatures, etc. are adjusted for particular treatment needs or for a particular product. Please see Box 1Ap.1
for guidance on the analytical methods than can be used for measuring emission factors.
Another approach would be for facilities to periodically (for short periods of time) install equipment to measureemissions from their stacks for purposes of developing facility-specific emission factors to estimate emissions
over the long term. It is very important to note that emission factors (i.e. input liquid utilization efficiencies andby-product formation rates) can be strongly affected by changes in process variables (e.g. type of textile
substrate material, curing temperature, liquid ratio, used chemical, processing time, etc.) and by the design of theprocess equipment. Thus, emission factors can substantially fluctuate from one tool manufacturer to another andfor a recipe ‘tuned’ for a particular purpose or product.

6 Textile auxiliaries are defined as chemicals of formulated chemical products which enable a processing operation in

preparation, dyeing, printing or finishing to be carried out more effectively or which is essential if a given effect is to beobtained.

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TABLE 1AP.4
INFORMATION SOURCES NECESSARY FOR COMPLETING THE TIERED EMISSIONS ESTIMATING METHODS FOR WET-BASEDTREATMENT OF TEXTILE, CARPET, LEATHER, AND PAPER
Tier 2
Data

Tier 1

Tier 3

Formation of volatile byproducts

Consumption of liquid input
chemicals

2aCi = liquor concentration for input chemical i(fraction, kg of input chemical i per kg of liquor).

Me/Mo

LPi = liquor pick-up for input chemical i (fraction,
kg of liquor containing input chemical i per kg oftextile substrate).

Me/Mo

Ci,p= liquor concentration for input chemical i andprocess p, (fraction, kg of input chemical i per kg
of liquor for process p).

Me/Mo

Me/Mo

LPi,p = liquor pick-up for input chemical i andprocess p, (fraction, kg of input chemical i per kg
of liquor for process p).

Me/Mo

Me/Mo

Da

Mea

Mea

Mea

D/Mea

D/Mea

Mea

Mea

Bk,i, = substance emission factor for volatile byproduct k for input chemical i (fraction, kg ofvolatile by-product formed per kg of input
chemical consumed)D

Bk,i,p = substance emission factor for volatile byproduct k for input chemical i and process p(fraction, kg of volatile by-product formed per kg
of input chemical consumed for process p)

Downstream FC Emission Control

ak, = fraction of by-product k produced in processes
with certified FC emission control technology

Meak,p, = fraction of by-product k produced fromprocesses p with certified FC emission control
technology
dk = Destruction Removal Efficiency (DRE) for byproduct k (per cent)

D/Medk.p = Destruction Removal Efficiency (DRE) for
by-product k for process p (%)
UT = Average uptime factor of all abatement
systems connected to process tools

Me

UTp = Average uptime factor of all abatement
systems connected to process tools running process
type pAnnual Production
Capacity2b

EFk = emission factor for volatile by-product k (kgof volatile by-product formed per kg of substrate
produced)D

Cu = fraction of annual plant production capacity
utilizationMe

Cd = annual manufacturing design capacity (kg of
substrate processed)

Me

Me = measurement; Mo = model {modelling criteria TBD}; D = Use default factors from guidance.
a{For the Tier 2b method ‘p’ is to be interpreted as a wet process type and/or a substrate type (see further discussion below)}. For the
Tier 3 ‘p’ is to be interpreted as a site-specific process.

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TIER 1 METHOD FOR WET PROCESSES – DEFAULTThe Tier 1 method is the least accurate estimation method and should be used only in cases where site-specificdata on the consumption of input chemicals are not available. The Tier 1 method, unlike the Tier 2a, 2b or Tier 3
methods, is designed to give an aggregated estimate of FC emissions although its methodology appears to
produce gas-specific emissions. As envisioned, Tier 1 estimates would be made simultaneously for all (or for themost important) gases listed in Tables 1Ap.1 and 1Ap.2 and can only be used if reported as a complete set.
As proposed, the Tier 1 calculation relies on a fixed set of generic emissions factors and does not account fordifferences among process and substrate types, individual processes or manufacturing tools. However, themembers of the set would likely differ depending on the surface area of textile, carpet, leather, or paper products
being manufactured. Each member of a set, which is a gas-specific emission factor, would express average
emissions per unit of substrate area (textile, carpet, leather, paper) produced during manufacture.
For any class of product, the factors (members of the set) are multiplied by the annual capacity utilization (Cu, afraction) and the annual manufacturing design capacity (Cd, in kg) of substrate processes. The product (Cu • Cd)
is an estimate of the quantity of substrate produced during the manufacture of textile, carpet, leather, or paper.
The result is a set of annual emissions expressed in kg of the volatile by-products that comprise the set for eachclass of products. The Tier 1 formula is shown in Equation 1Ap.10.
In using Tier 1, inventory compilers should not modify, in any way, the set of the FC assumed to represent
average emissions. Further, as is common practice for IPCC methods, the Tier 1 method does not allow to accountfor the use of emissions control technologies, and inventory compilers should not combine emissions estimatedusing Tier 1 method with emissions estimated using the Tier 2 or 3 methods. Neither may inventory compilers
use, for example, the Tier 1 factor for 1,1,2,2-Tetrafluoroethyl methyl ether to estimate the emissions of 1,1,2,2Tetrafluoroethyl methyl ether from pad-dry-cure textiles and combine it with the results of other FC gases from a
Tier 2 or Tier 3 method. The formula used to calculate Tier 1 emissions is shown in Equation 1Ap.10.

EQUATION 1AP.10
TIER 1 METHOD FOR ESTIMATION OF THE SET OF FC EMISSIONS{FCk }n= {EFk • Cu • Cd }n(k= 1,..., n)

Where:{𝐹𝐹𝐹𝐹𝑘𝑘 }𝑛𝑛 = emissions of FC volatile by-product k (kg)Note: { }n denotes the set for each class of products (e.g. textile, carpet, leather, or paper) and n denotes
the number of volatile by-products included in each set (see Tables 1Ap.1 and 1Ap.2) The estimates
are only valid if made and reported for all members of the set using this Tier 1 methodology
𝐸𝐸𝐸𝐸𝑘𝑘= FC emission factor for volatile by-product k expressed as annual mass of emissions per mass of
substrate for the product class (mass of volatile by-product k emitted, in kg/kg)

𝐶𝐶𝑑𝑑= annual manufacturing design capacity, kg of substrate processed𝐶𝐶𝑢𝑢= fraction of annual plant production capacity utilization, fraction

TIER 2A METHOD FOR WET TREATMENT PROCESSES – PROCESSCHEMICAL-SPECIFIC PARAMETERS
The Tier 2a method uses industry-wide default values for the ratio of the mass of chemical i evaporated divided
by the mass of chemical i used (EVi), the mass fraction of volatile by-product k formed from the use of liquid
input chemical i (Bk,i), the liquor concentration (Ci), the liquor pick-up (Li), the fraction of input chemical i usedin the wet-based manufacturing process (Di) and the fraction of FC by-products k destroyed by the emissions
control technology (Dk). The Tier 2a method also calculates emissions for each input chemical used on the basisof site-specific data on chemicals consumption and emissions control technologies. Thus, to use the Tier 2amethod, inventory compilers must have direct communication with industry (e.g., annual emissions reporting) togather consumption data and ensure that emission control technologies are installed and used in accordance withthe guidelines provided in this document. Unlike the Tier 2b and Tier 3 methods that are explained later in thissection, the Tier 2a method does not distinguish between process or substrate types, or site-specific processes.
However, the Tier 2a default emission factors are formed separately for each input chemical, which, unlike theTier 1 method, allows to account for the actual mix of input chemicals used at a particular site. Total Tier 2aAp1.162019 Refinement to the 2006 IPCC Guidelines for National Greenhouse Gas Inventories

Appendix 1: Basis for Future Methodological Development

emissions are equal to the sum of emissions from evaporative losses of unreacted fluorinated chemicals i in the
production process (Ei) plus emissions of all by-products k (BPEk) resulting from the conversion of all input
chemicals i used during production, as calculated using equations 1Ap.11, and 1Ap.12 below.

EQUATION 1AP.11
TIER 2A ESTIMATION OF EMISSIONS OF UNREACTED INPUT CHEMICALSEi = Ci • LPi • EVi • (1 − Di )Where:𝐸𝐸𝑖𝑖 = emissions of unreacted input chemical i through evaporative losses, kg
𝐶𝐶𝑖𝑖= liquor concentration, kg of input chemical i per kg of liquor

𝐿𝐿𝐿𝐿𝑖𝑖 = liquor pick-up, kg of liquor containing input chemical i per kg of textile substrate

𝐸𝐸𝐸𝐸𝑖𝑖 = ratio of the mass of chemical i evaporated divided by the mass of chemical i used

𝐷𝐷𝑖𝑖 = overall reduction of chemical i, fraction, calculated per equation 1Ap.13 (replacing 'k' indices by 'i'
indices).
EQUATION 1AP.12
TIER 2A ESTIMATION OF BY-PRODUCT EMISSIONS

=
BRE
k

∑ B • C • LP • (1 − D )
i

k, i

i

i

k

Where:𝐵𝐵𝐵𝐵𝐵𝐵𝑘𝑘 = textile-based emissions of volatile by-product k generated from the conversion of all input
chemicals i per mass of textile substrate, kg/kg
𝐵𝐵𝑘𝑘,𝑖𝑖= substance emission factor, kg of volatile by-product k created per kg of input chemical i
consumed

𝐿𝐿𝐿𝐿𝑖𝑖= liquor pick-up, kg of liquor containing input chemical i per kg of textile substrate𝐶𝐶𝑖𝑖= liquor concentration, kg of input chemical i per kg of liquor

𝐷𝐷𝑘𝑘 = overall reduction of by-product k emissions, fraction, calculated per equation 1AP.13
EQUATION 1AP.13
EMISSIONS REDUCTION IMPACT OF EMISSIONS CONTROL TECHNOLOGY

Dk = ak • d k • UT
Where:
𝐷𝐷𝑘𝑘 = overall reduction of volatile by-product k emissions, fraction

𝑎𝑎𝑘𝑘 = fraction of by-product k produced from processes with emission control technologies (site-specific),
fraction
𝑑𝑑𝑘𝑘 = Destruction Removal Efficiency (DRE) for by-product k, fraction

𝑈𝑈𝑈𝑈 = average uptime of all abatement systems, fraction, calculated per Equation 1AP.14

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Ap1.17Volume 3: Industrial Processes and Product Use

EQUATION 1AP.14
UPTIME OF EMISSION CONTROL SYSTEMUT = 1 −

∑ Td
∑ UT
n

n

n

n

Where:𝑈𝑈𝑈𝑈 = average uptime factor of all abatement systems connected to process tools, fraction

𝑇𝑇𝑇𝑇𝑛𝑛 = The total time, in minutes, that abatement system n connected to process tool(s) in the plant, is not
in operational mode when at least one of the manufacturing tools connected to abatement system n is
in operation
𝑈𝑈𝑈𝑈𝑛𝑛 = total time, in minutes per year, in which abatement system n has at least one associatedmanufacturing tool in operation. UT may be set to 1 if suitable backup abatement or interlocking
with the process tool is implemented for each abatement system. 7n= abatement system

TIER 2B METHOD FOR WET PROCESSES – PROCESS / SUBSTRATE
SPECIFIC PARAMETERS
The Tier 2b method is similar to the Tier 2a approach in the sense that it is based on chemical-specific default
emission factors, but the Tier 2b factors also account for the types of wet processes and/or classes of products.
For the definition of ‘p’ compilers should refer to Box 1AP.2 Thus, the Tier 2b approach is expected to be moreaccurate than the Tier 2a one because the Tier 2b method reflects the type of processes used or products made ina particular manufacturing facility. Also, the Tier 2b method allows to account for the trend where somechemicals tend to be used predominantly in particular process types or products manufactured. The Tier 2b
method uses industry-wide default values for the ratio of the mass of chemical i evaporated divided by the massof chemical i used during process type or product type p (EVi,p), the for the mass fraction of volatile FC byproduct k formed from the use of input chemical i per mass of substrate in process type or product type p (Bk,i,p),the liquor concentration (Ci,p) for substrate in process type or product type p, the liquor pick-up (Li,p) for
substrate in process type or for product type p, the fraction of input chemical i used in the wet-based
manufacturing process using process type or product type p and the fraction of chemical i evaporated or FC byproducts k destroyed by the emissions control technology connected to tools using process type or product type p(Di,p and Dk,p).

7 For determining the amount of tool operating time, you may assume that tools that were installed for the whole of the year

were operated for 525,600 minutes per year. For tools that were installed or uninstalled during the year, you should prorate
the operating time to account for the days in which the tool was not installed; treat any partial day that a tool was installed
as a full day (1,440 minutes) of tool operation. For an abatement system that has more than one connected tool, the tool
operating time is 525,600 minutes per year if at least one tool was installed at all times throughout the year. If you havetools that are idle with no gas flow through the tool for part of the year, you may calculate total tool time using the actual
time that gas is flowing through the tool.

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Appendix 1: Basis for Future Methodological Development

BOX 1AP.2
APPROACHES FOR DERIVING THE TIER 2B EMISSION FACTORS AND DEFINING ‘P’

Two approaches are proposed. A first approach would be to provide separate Tier 2b emission
factors depending on the actual wet treatment method used in the process. In this case, default EFs
would be provided for process types such as wet finishing (e.g. pad-dry-cure and exhaust
applications), low wet pickup finish applications (e.g. vacuum extraction and kiss roll), spray
application, foam finishing, coating, and lamination.
Another approach would be to provide separate Tier 2b emission factors based on the type of
product manufactured. In this case, default EFs would be provided for substrate types such as
cellulosic and regenerated cellulosic textiles (cotton, viscose, rayon, etc.), synthetic polymers for
textile (polyamides, polyesters, polypropylenes, polyurethane), lignocellulosic (flax, jute, sisal,etc.), protein-based textiles (wool, silk), leather, paper and paperboard, and technical textile
polymers.
The information currently available is insufficient to determine which of the two approaches above(or a combination thereof) might be most suitable, or if separate methods should be provided to
distinguish EFs by process type (a separate Tier 2b method) and by product type (an additional
Tier 2c method). Further discussion is required on this point, and an analysis of how emission
factors may be grouped based on different treatment process conditions (temperature, timing, typeof chemicals used, etc.) should be conducted. Nevertheless, the Tier 2b methodological framework
proposed here could be adapted to the (to be determined) best approach.

Although the Tier 2b method is preferred over the Tier 2a method because process-type-specific or product-typespecific emission factors are more accurate, it should be noted that the Tier 2b method presents increased
complexity because the consumption of input chemicals must be allocated to each process or product type p.
Thus, in the case where the consumption of input chemicals cannot directly be measured for each process type or
product type p, a chemical consumption allocation model must be devised for applying the method, 8 andinventory compilers should consider the trade-off of using more accurate process-specific or product-specificemission factors versus introducing errors in the Tier 2b estimate, due to uncertainties in the allocation model.
Total Tier 2b emissions are equal to the sum of emissions from evaporative losses of unreacted fluorinatedchemicals i used in all production processes p (Ei) plus emissions of all by-products k (BPEk) resulting from theconversion of all input chemicals i used during the production of process types or substrate types p, as calculatedusing equations 1Ap.15, and 1Ap.16 below.

EQUATION 1AP.15
TIER 2B ESTIMATION OF EMISSIONS OF UNREACTED INPUT CHEMICALS

=
Ei

∑ C
p

i, p

• LPi , p • EVi , p • (1 − Di , p ) 

Where:
𝐸𝐸𝑖𝑖= emissions of unreacted input chemical i through evaporative losses, kg

𝐶𝐶𝑖𝑖,𝑝𝑝 = liquor concentration, kg of input chemical i per kg of liquor for production process p

𝐿𝐿𝐿𝐿𝑖𝑖,𝑝𝑝 = liquor pick-up, kg of liquor containing input chemical i per kg of textile substrate for production
process p

𝐸𝐸𝐸𝐸𝑖𝑖,𝑝𝑝 = ratio of the mass of chemical i evaporated divided by the mass of chemical i used

𝐷𝐷𝑖𝑖,𝑝𝑝 = overall reduction of chemical i using production process p, fraction, calculated per equation
1AP.17 (replacing 'k' indices by 'i' indices)
8 For an example of how site-specific gas consumption allocation models can be developed, please see Chapter 6 Volume 3of the 2019 Refinement.

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Ap1.19Volume 3: Industrial Processes and Product Use

EQUATION 1AP.16
TIER 2B ESTIMATION OF BY-PRODUCT EMISSIONS

=
BREk

∑

i, p

 Bk , i , p • Ci , p • LPi , p • (1 − Dk , p ) 

Where:𝐵𝐵𝐵𝐵𝐵𝐵𝑘𝑘 = textile-based emissions of volatile by-product k generated from the conversion of all input
chemicals i per mass of textile substrate used for all production processes p, kg/kg
𝐵𝐵𝑘𝑘,𝑖𝑖,𝑝𝑝 = substance emission factor, kg of volatile by-product k created per kg of input chemical i
consumed used for production process p𝐶𝐶𝑖𝑖,𝑝𝑝= liquor concentration, kg of input chemical i per kg of liquor for production process p

𝐿𝐿𝐿𝐿𝑖𝑖,𝑝𝑝 = liquor pick-up, kg of liquor containing input chemical i per kg of textile substrate for production
process p

𝐷𝐷𝑘𝑘,𝑝𝑝 = overall reduction of volatile by-product k emissions from tools using production process p,
fraction, calculated per Equation 1Ap.17
EQUATION 1AP.17
EMISSIONS REDUCTION IMPACT OF EMISSIONS CONTROL TECHNOLOGY

Dk , p = ak , p • d k , p • UTp
Where:
𝐷𝐷𝑘𝑘,𝑝𝑝 = overall reduction of volatile by-product k emissions produced from production process p, fraction

𝑎𝑎𝑘𝑘,𝑝𝑝 = fraction of by-product k volume produced from production process p with emission control
technologies (site-specific), fraction

𝑑𝑑𝑘𝑘,𝑝𝑝 = Destruction Removal Efficiency (DRE) for by-product k and production process p, fraction

𝑈𝑈𝑈𝑈𝑝𝑝 = average uptime of all abatement systems connected to tools using production process p, fraction,
calculated per Equation 1Ap.18
EQUATION 1AP.18
UPTIME OF EMISSION CONTROL SYSTEMSUTp = 1 −

∑ Td
∑ UT
n

n, p

n

n, p

Where:𝑈𝑈𝑈𝑈𝑝𝑝= average uptime factor of all abatement systems connected to process tools running production
process p, fraction

𝑇𝑇𝑇𝑇𝑛𝑛,𝑝𝑝 = The total time, in minutes, that abatement system n connected to process tool(s) running
production process p in the plant, is not in operational mode when at least one of the
manufacturing tools connected to abatement system n is in operation
𝑈𝑈𝑈𝑈𝑛𝑛,𝑝𝑝 = total time, in minutes per year, in which abatement system n has at least one associatedmanufacturing tool running production process p in operation. UT may be set to 1 if suitable

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Appendix 1: Basis for Future Methodological Development

backup abatement or interlocking with the process tool is implemented for each abatement
system 9n= abatement system

TIER 3 METHOD FOR WET PROCESSES – SITE-SPECIFIC PARAMETERS
The Tier 3 method uses the same set of equations (equations 1Ap.15 to 1Ap.18) as the Tier 2b method. However,when using the Tier 3 method, inventory compilers need to interpret ‘p’ in these equations as a specificproduction process using a specific ‘recipe’. A recipe corresponds to a particular combination of input liquids
under specific conditions of process duration, temperature, type of substrate, and other relevant processparameters adjusted to achieve a particular result (e.g. water or stain resistance). It is very important to note thatemission factors and by-product formation rates can be strongly affected by changes in process parameters(temperature, flows and nature of input chemicals, processing time, etc.).
When using the Tier 3 method, BPE emission factors in Equation 1Ap.16 should be measured for specificprocesses recipes. However, a centreline process recipe may be used to establish Tier 3 emission factors for setsof ‘similar’ recipes. Recipes can be deemed ‘similar’ when the centreline process can reasonably be deemed
representative of facility-specific process conditions, of the potential variability of such process conditions
around the centreline process during normal manufacturing operations, and when the substrate, process type,product, process tool, and input process gases are the same. When using the concept of ‘similarity’, inventory
compilers should be able to reasonably demonstrate that emissions estimates are not biased (i.e. systematicallyover- or under-estimated) when using centreline process recipe(s) emission factors.
Once default Tier 2a or Tier 2b emission factors will be developed, the Tier 3 method should be used bymanufacturing plants whose processes and recipes depart significantly from industry-wide patterns of use, or by
manufacturing plants that may have developed specific processes whose characteristics may result in asignificantly lower or higher utilization of input chemicals or formation of by-products. Further, if default Tier 2emission factors are not available for a particular process or input chemical, manufacturing facilities shouldmeasure their site-specific emission factors and use the Tier 3 method.
It should also be noted that Tier 3 emission factors could be combined with Tier 2a or 2b default emission
factors (once available) to use a hybrid method. A hybrid method would involve applying the Tier 2 defaults toprocesses and technologies that have not changed while applying Tier 3a, site-specific emission factors toprocesses and technologies that have changed. Indeed, higher accuracy might be achieved by using the Tier 3
method for specific input chemicals or site-specific processes. However, inventory compilers should not
combine the Tier 1 method with any other method.
The Tier 3 method is not outlined further in this Appendix, but inventory compilers should refer to the Box
1.Ap.1 on specific technologies for the measurement of FC emissions in order to develop facility- or countryspecific emission factors as a resource for implementing the Tier 3 method.

1A.3

Choice of emission factors

At the moment no representative FC emissions data can be obtained for textile, carpet, leather and paperindustries to derive the Tier 1 or Tier 2 default emission factors. Thus, the Tier 3 methods is the only practicalmeans to estimate emissions from this sector, where individual manufacturing sites will have to use measured
emission factors (equipment-specific, process-specific, or site-specific). In this case, applying the Tier 3 methods
and reporting emission factors across representative manufacturing sites will become essential in building a
database of emission factors that can later be used to derive the Tier 1 and Tier 2 emission factors. Countries areencouraged to develop country-specific emission factors based on surveys of representative subsets of sources.
Countries are also encouraged to work with equipment manufacturers and users of such equipment to measure

9 For determining the amount of tool operating time, you may assume that tools that were installed for the whole of the year

were operated for 525,600 minutes per year. For tools that were installed or uninstalled during the year, you should prorate
the operating time to account for the days in which the tool was not installed; treat any partial day that a tool was installed
as a full day (1,440 minutes) of tool operation. For an abatement system that has more than one connected tool, the tool
operating time is 525,600 minutes per year if at least one tool was installed at all times throughout the year. If you havetools that are idle with no gas flow through the tool for part of the year, you may calculate total tool time using the actual
time that gas is flowing through the tool.

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Ap1.21Volume 3: Industrial Processes and Product Use

equipment-specific, process-specific, or site-specific emission factors, with the aim of developing representative
default emission factors that could eventually be used for site-specific, domestic, or industry-wide inventories. It
is good practice to clearly and transparently document such emission factors. To support development ofrepresentative default emission factors, inventory compilers are encouraged to submit measurements of emission
factors to the IPCC Emission Factor Database (EFDB).

1A.4

Choice of activity data

Activity data for the textile, carpet, leather and paper industries consist of data on gas or finishing agent
sales/purchases and/or production figures (surface area or kg of substrate used during the textile treatments). For
plasma and wet-based treatments the more data-intensive Tier 2 and Tier 3 methods, gas consumption andfinishing agent data at the company or plant-level are necessary. The preferred methodologies for data collection
are described in Box 1Ap.1. For Tiers 2 and 3, countries should create a national textile industry database with
relevant data or information on textile companies, types of production/treatment, annual production data,
consumption of chemicals and other relevant parameters. For the Tier 1 methods, inventory compilers will needto determine the total surface area of textile substrates treated during the reporting year for plasma or the mass oftextile substrates treated for wet-based processes in the reporting year. The best sources of either gas/finishing
agent usage data or substrate area per kg data are the owners and operators of the textile manufacturing facilities
in each country.

1A.5

Reporting and Documentation

It is good practice to document and archive all information required to produce equipment-specific, processspecific or site-specific emission factors and national emission inventory estimates as outlined in Volume 1,
Section 6.11. The inventory should include summaries of methods used and references to source data such thatthe reported emission estimates are transparent and steps in their calculation may be retraced. It is suggested that
any inventory value outside the 95 percent confidence range of the data population variance be confirmed withthe data source. Use of standard measurement methods improves the consistency of the resulting data andknowledge of the statistical properties of the data. Large differences should be explained and documented. In
addition, the methods applied and references should be documented. It is good practice to conduct quality
control checks and quality assurance procedures as outlined in Volume 1, Chapter 6. Inventory compilers areencouraged to use higher tier Quality assurance and quality control (QA/QC) for key categories as identified inVolume 1, Chapter 4. Transparent reporting of emissions factors will be required to ensure that representative
default emission factors can be derived. Efforts to increase transparency should also take into account theprotection of confidential business information related to specific gases or finishing agents used.

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Appendix 1: Basis for Future Methodological Development

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2019 Refinement to the 2006 IPCC Guidelines for National Greenhouse Gas Inventories

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