Next Article in Journal
The Spatio-Temporal Distribution Characteristics of Carbon Dioxide Derived from the Trajectory Mapping of Ground Observation Network Data in Shanxi Province, One of China’s Largest Emission Regions
Next Article in Special Issue
Air Quality Monitoring with Low-Cost Sensors: A Record of the Increase of PM2.5 during Christmas and New Year’s Eve Celebrations in the City of Queretaro, Mexico
Previous Article in Journal
Synoptic-Scale Wildland Fire Weather Conditions in Mexico
Previous Article in Special Issue
Enhanced Sulfate Formation from Gas-Phase SO2 Oxidation in Non–•OH–Radical Environments
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Atmosphere
Volume 15
Issue 1
10.3390/atmos15010097
atmosphere-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Review

Light-Duty Vehicle Brake Emission Factors

by
Barouch Giechaskiel
1,*,
Theodoros Grigoratos
1,
Panagiota Dilara
2,
Traianos Karageorgiou
3,
Leonidas Ntziachristos
4 and
Zissis Samaras
4
1
European Commission, Joint Research Centre (JRC), 21027 Ispra, Italy
2
European Commission, DG-ENV, 1160 Brussels, Belgium
3
Emisia, 55535 Thessaloniki, Greece
4
Mechanical Engineering Department, Aristotle University of Thessaloniki, 54124 Thessaloniki, Greece
*
Author to whom correspondence should be addressed.
Atmosphere 2024, 15(1), 97; https://doi.org/10.3390/atmos15010097
Submission received: 20 December 2023 / Revised: 7 January 2024 / Accepted: 10 January 2024 / Published: 11 January 2024
(This article belongs to the Special Issue Chemical Composition and Sources of Particles in the Atmosphere (2nd Edition))
Browse Figures
Versions Notes

Abstract

:
Particulate Matter (PM) air pollution has been linked to major adverse health effects. Road transport still contributes significantly to ambient PM concentrations, but mainly due to the non-exhaust emissions from vehicles. For the first time worldwide, limits for non-exhaust emissions have been proposed by the European Union for the upcoming Euro 7 step. For these reasons, interest in brake emissions has increased in the past few years. Realistic emission factors are necessary to accurately calculate the contribution of brake emissions to air pollution but also to estimate the emissions reduction potential of new or existing technologies and improved brake formulations. This paper reviews emission factors from light-duty vehicles reported in the literature, with a focus on those that followed the recently introduced Global Technical Regulation (GTR 24) methodology on brakes in light-duty vehicles. Reduction efficiencies of non-asbestos organic (NAO) pads, brake dust filters, ceramic discs, coated discs, and regenerative braking are also discussed. Finally, the emission factors are compared with roadside measurements of brake emissions and emission inventories worldwide. The findings of this study can be used as an input in emission inventories to estimate the contribution of brakes to air pollution.

1. Introduction

Particulate Matter (PM) is a pollutant with adverse health effects. In 2019, exposure to PM with aerodynamic diameter < 2.5 μm (PM2.5) was responsible for 7% of total global mortality (4.1 million deaths) [1]. In Europe, the contribution of road transport to ambient PM has decreased in the last decades from over 20% [2] to around 10% [3]. This can be largely attributed to the reduction of vehicle exhaust emissions, in particular due to the addition of Diesel particulate filters (DPFs) at the vehicles’ aftertreatment systems since 2011 with Euro 5b. Although exhaust PM emissions are continuously decreasing over time due to fleet electrification, non-exhaust PM emissions (i.e., emissions from brakes, tires, and road) have slightly increased. The recent Euro 7 Impact Assessment study [4] has highlighted this issue by illustrating the expected evolution of PM emissions from exhaust and non-exhaust sources in the European Union (EU27) until 2050, assuming no emission control technologies are implemented for non-exhaust emissions (Figure 1). The increasing trend in non-exhaust emissions has also been demonstrated by data reported from the EU vehicle emission inventories until 2021 [5,6] and beyond [7,8]. National emission inventories primarily focus on primary particles, segregating PM emissions from tire and brake wear (nomenclature for reporting (NRF) 1A3bvi) and road abrasion (NRF 1A3bvii) from exhaust PM emissions [9]. Resuspended PM of the previously deposited material is not considered a primary source of emission and is not included in Figure 1 in order to avoid double-counting. Brakes contribute 30% (PM2.5) to 40% (PM10) to non-exhaust emissions. According to Figure 1, non-exhaust emissions accounted for 30% (PM2.5) to 45% (PM10) in 2010, 54% (PM2.5) to 69% (PM10) in 2020 (after introduction of DPFs), and will exceed 90% in 2040. This is the reason that the European Commission proposed to introduce limits for reducing brake and tire wear with Euro 7.
Brake wear particles come mainly from the friction between the brake pad/shoe and disc/drum. A considerable part of the order, 40%, becomes airborne PM [10]. There are two main friction brake system configurations in current use: disc brakes, in which flat brake pads are forced against a rotating metal disc and drum brakes, in which curved brake shoes are forced against the inner surface of a rotating cylinder. Cars are usually equipped with front disc brakes and either rear disc or drum brakes. Commercial vehicles tend to be fitted with drum brakes, although disc brakes are being introduced by some manufacturers. Drum brakes in Europe are estimated to cover 10% of the brake market.
Gray (or grey) cast iron (GCI) is a popular automotive brake disc material due to its high melting point, good heat storage and damping capability, and good castability and machinability [11,12]. However, poor corrosion resistance and excessive wear result in high brake particle emissions. For example, a study found that the effect of corrosion inhibited braking performance by reducing the coefficient of friction and significantly increased both the number and mass of particle emissions by at least a factor of 2 and up to 30 times compared with the uncorroded disc under the same test conditions [13]. Various treatments (e.g., cryogenic, heat) can improve the tribological properties and reduce the wear [14]. Surface treatment in the form of a suitable coating (e.g., with hard metal coating (HMC) such as tungsten carbide, cobalt, chrome) is a promising solution [11,15]. Carbon–ceramic discs (CC) are another option, but more costly. The market penetration of CC and HMC discs is currently limited to high-performance sports cars and luxury class vehicles due to their high costs. However, it is becoming a very popular method for reducing the amount of particles formed. Replacing GCI with CC or coated discs reduces the emissions due to lower disc wear. The pads wear is also reduced (e.g., [16]), but in some cases, it can even increase [17]. For this reason, the use of such discs in vehicles is accompanied by research to develop the appropriate pads. It is noteworthy that some studies demonstrated low reductions from GCI replacement with CC or coated discs [18]. Even though the cost is quite high, the future cost of coated discs is estimated between 3.5 and 16 Euros per disc [19].
Brake pad materials can be categorized based on their friction material as organic, or metallic. Other categories include ceramic (expensive), carbon (only for high temperatures) and aluminum (only for light applications and rear brakes) but they are not widespread [20]. The metallic pads are sub-divided in low-metallic (LM) or low steel, semi-metallic (SM) or fully metallic (not common). Thus, in the literature, the pads are practically categorized as: non-asbestos organic (NAO), LM or SM [21,22]. Recently, non-metallic (NM) pads have been reported [12], but they refer to NAO pads [23]. The Economic Commission for Europe (ECE) refers to European performance brake pads (usually LM or SM). The United States of America (USA), Japan and Korea markets typically use NAO pads. Older and recent measurements indicated that replacing ECE with NAO pads can reduce PM from brakes [24,25].
As brake wear occurs mainly when braking, the highest concentrations of brake wear particles should be observed in urban areas, in particular at traffic lights, pedestrian crossings and corners. Particles may also be released from the brake mechanism or wheel housing sometime after the primary emission event. Finally, emissions due to the remaining drug force in non-braking events have been reported [26].
Various options exist for the reduction of brake emissions: Better pad and disc materials, vehicle light-weighting, capturing particles in the brake (e.g., drum brake or passive and active filters), reduced friction braking (e.g., regenerative braking or predictive braking) and reduction of drag torque [27,28].
Emission factors are based on specific brake measurements or on roadside measurements and source appointment. However, the experimental data on which the emission factors of the inventories are based on are limited and in some cases outdated. Even though the first studies on brake emissions date back in the 1980s [29], the topic was of low importance until the exhaust emissions decreased to levels comparable with the non-exhaust emissions.
For the determination of emission factors, measurements can be done in the laboratory (e.g., Pin-on-Disc (PoD), brake dynamometer) and on the vehicle (chassis dynamometer, on-road) using various instruments (gravimetric filter method, optical counters, electrical counters, etc.) and different driving cycles. Common cycles in the laboratory are the 3 h-Los Angeles City Traffic (3 h-LACT), Worldwide harmonized light vehicle test procedure cycle designed for exhaust emissions (WLTP-E) [30], or the one designed for brake emissions (WLTP-B) [31]. The various studies used different test conditions (ambient temperature, simulated vehicle weight), depending on their needs. The recent Global Technical Regulation (GTR 24) on brake emissions from light-duty vehicles standardized the measurement procedures. This UN GTR defines the test cycle, minimum system requirements, test conditions, and equipment preparation to execute the WLTP-B cycle using brake dynamometers. The Euro 7 proposal with brake limits is based on this methodology. The GTR 24 was developed by the Particle Measurement Programme (PMP) informal working group under the auspices of the United Nations Economic Commission for Europe (UNECE) Working Party on Pollution and Energy (GRPE), which started working on the topic in 2013. Until that period, there were only a few reviews [32], but since 2011 there have been numerous studies on brake emissions [22,33,34,35,36,37,38,39,40,41,42,43].
Aim of this comprehensive review is to summarize all studies on brake emissions and, in particular, those recent studies following the GTR 24 standardized methodology. The ultimate goal is to provide up-to-date PM2.5, PM10 and particle number (PN) emission factors for light-duty vehicles and reduction potential of pads, discs and regenerative braking.

2. Background

Table 1 summarizes in chronological order the experimental studies that provided emission factors based on direct measurements. Most of them have been mentioned in previous reviews. Additional information regarding the test cycles and the instrumentation that was used is given. Studies that gave results in volume units (e.g., mg/m3) and did not express the results per distance (i.e., mg/km) are not included. These studies are summarized elsewhere (e.g., [43]). It is evident that due to the methodological differences, test cycles, and instrumentation, a direct comparison is difficult. Nevertheless, emission inventories emission factors are based partly on these data.
The values of Table 1 refer to vehicle level. To convert front brake corner emissions to vehicle emissions, a factor of 2.83 was used, whenever no other information was provided. This value is based on the GTR 24 brake force distribution of front and rear axles of 77%/32%: if the emissions of the front brake are known, then the vehicle emissions can be calculated using the factor (77% + 32%)/(77%/2) = 2.83. Quite often the ratio 70%/30% is used, which results in a factor of (70% + 30%)/(70%/2) = 2.85, or sometimes the rounded value of 3 is used.

3. Research According to GTR 24

This section summarizes the research, following as closely as possible the light-duty vehicles Brakes GTR 24. The main requirements are: testing of a brake assembly in an enclosure, using a brake dynamometer, and following the WLTP-B (brake) cycle. Sampling from a tunnel using cyclonic separators is followed by filters for PM and condensation particle counters (CPC) for PN. Here, PN refers to total PN > 10 nm, but only when the measured values were close to the solid PN. Cases with high PN have been excluded (and will be discussed separately in the Discussion section).
When comparing pads, discs, or technologies, other studies deviating from the GTR are also included, as the relative difference is of interest.
The studies are those found in the literature, without any information regarding their representativeness or coverage of the market.

3.1. Emission Factors per Brake Corner

Table 2 summarizes the research that followed the Brakes GTR 24 (or very similar). The averages and different scenarios will be presented in Section 4.

3.2. Mass (Wear) Loss and Airborne Fraction

Not all mass (wear) that is lost from the pad and the disc becomes airborne. The airborne fraction, sometimes called the total suspended fraction, has been determined in some studies and is summarized in Table 3. On average, it is around 40%. Most of the airborne fraction is PM10 (typically ≫ 80%). For this reason, in some cases, airborne to mass loss or PM10 to mass loss ratios are used interchangeably. A few studies found ratios of PM10 to mass loss < 30%, but recent studies found ratios > 30%, on average 42%. This value should be lower than the airborne fraction, but it is based on different studies. Thus, the experimental conditions and the brakes were different. The three common studies reported that PM10 is 80–98% of total airborne PM. Combining the two numbers together, it can be concluded that the airborne and PM10 fractions account for on average 40–42% of the total wear. A study showed that theoretically, the 43% fraction corresponds to a mass median diameter of around 6.3 μm [79]. The same study summarized measured size distributions, and in agreement with other reviews [8,33] the mass peak is expected in the 3–6 μm range.

3.3. PM2.5 to PM10

Based on the studies of Table 2, the ratio of PM2.5 to PM10 is 40% for ECE pads, 45% for NAO pads, 59% for CC and HMC discs, and 60–100% for drum brakes. The high percentage of drum brakes could be due to the low masses collected on the filters and the respective experimental uncertainty. A study found that while the ratio was 43% for the WLTP-B cycle, for other cycles the ratio varied from 33% to 70% [23]. Theoretically the 45% ratio corresponds to mass distribution with a peak at 3 μm [79].

3.4. ECE vs. NAO Pads

Many studies have demonstrated that the pad’s composition has an impact on wear and particle formation (see studies in review [80]). From the previous section, it is evident that NAO pads have lower emissions than ECE (metallic) pads. This was demonstrated as early as 2000 [46]. An older study also showed that the disc mass loss can also be reduced by replacing LM with NAO pads [24]. NAO pads are typically used in USA, Japan and Korea, while ECE pads are typically used in Europe.
Table 4 summarizes the studies that investigated the impact of pad material on brake emissions. On average, the reduction is 62% for PM10, 55% for PM2.5 and 64% for PN when comparing NAO against ECE materials. However, the scatter of emission reductions is large due to the high variability of the (absolute) emission levels of the ECE pads. In other words, replacing a high-emitting ECE pad and a low-emitting ECE pad with the same NAO pad, will most likely result in different reduction efficiencies.

3.5. Advanced Discs

GCI discs are popular due to their advantages but, at the same time, are associated with high wear. In general, in GCI with ECE high-emitting brakes, the disc contributes around 60% to total mass loss [16,77,82,83]. With drum brakes, the contribution is lower; one study found 37% [83]. However, with ceramic discs, the contribution of disc wear to total wear is much lower (<5%) [16].
Table 5 summarizes studies that investigated the impact of using carbon-ceramic (CC) or coated (HMC) discs instead of GCI discs on brake emissions. On average, the PM10 reduction is 81% for CC and 57% for HMC (70% for both CC and HMC) discs. The PM2.5 reduction is 74% for CC and 60% for HMC (70% for both CC and HMC) discs. For PN the reduction is 61% for CC and 57% for HMC (59% for both CC and HMC) discs.

3.6. Brake Particle Filters or Collection Systems

In recent years, brake particle collection filters appeared in the market with promising results. The systems can be active (sucking) or passive. Table 6 summarizes the studies and the resulting brake particle filtration (collection) efficiencies. On average, passive systems have a PM efficiency of 50%, while active systems 75%. However, for more accurate estimates of filtration efficiency, more studies are necessary with commercially available systems. The relatively low collection efficiency with active systems, which are not operating for the whole cycle, has to do with the off-brake emissions due to drag torque and axial vibrations. A study found that during the full WLTP cycle, 40–53% of the particles were emitted outside braking (off-brake emissions) [76].

3.7. Electrified Vehicles

Electrified vehicles’ sales and market share are increasing as EU is pacing to zero CO2 tailpipe emissions by 2035. Brake emissions (as well as other non-exhaust emission) from electrified vehicles are expected to increase due to their higher mass, but on the other hand to decrease due to their regenerative braking and hence reduced use of friction brakes [93]. Most studies estimate weight increases of electric vehicles in the order of 15–25% (250–320 kg) [93,94]. However, due to the increasing sale shares of SUVs in the ICE fleet, the average masses of conventional and electrified vehicles may get closer [95]. A study estimated that due to the additional mass of electrified vehicles, regenerative braking of 20–60% was necessary to bring the PM10 emissions at the same levels with the full friction counterparts [94]. Many researchers have predicted the reduction of emissions due to regenerative braking, typically between 50% and 95% [58,96]. A study assumed that electric vehicles require about two-thirds less friction braking than internal combustion vehicles, based on the roughly two-thirds longer service times of brake pads than of diesel/petrol vehicles [97]. Another study measured 60% recuperation of braking kinetic energy at smooth braking but only 8% for hard braking from 97 to 0 km/h for mild and plug-in hybrid vehicles [98]. Based on the brakes GTR 24 the reduction of the emissions is expected to be proportional to the use of the friction brakes. Table 7 gives the expected regenerative braking based on the friction braking share coefficients c in the GTR (1 − c). Furthermore, the fleet composition in 2020 is given based on European Commission’s (EC) impact assessment study [4], which is in agreement with e.g., ACEA’s report [99].
The experimental studies on brake emission factors with electrified vehicles are limited and summarized in Table 8. The emission factors as absolute values are lower compared to Table 2, which were based on full friction braking. Also, compared to their ICE counterparts the reductions are typically > 60% (Table 8).

4. Discussion

Section 2 summarized studies that provided emission factors following various methodologies. Section 3 summarized a large number of studies with brake emission factors following the recently introduced laboratory procedure of the GTR 24. Unfortunately, as it was mentioned, the market share of each brake is not known. Nevertheless, it can be assumed that the tested brakes are representative of the brakes in the market at the time of writing this paper. Differences of pad and disc materials, reductions with filters and regenerative braking were also summarized. Percentages of PM2.5 and PM10 to airborne PM and total mass (wear) loss were also provided. This Section 4 will present emission factors estimations, and the data will be compared with other datasets, roadside studies and emission inventories.

4.1. Emission Factors and Vehicle Mass

In general brake wear and kinetic energy change or brake dissipation energy are correlated [23,51,74,103]. For the same braking events (i.e., cycles), the brake wear should correlate with the load (vehicle mass). The impact of vehicle mass on the brake emissions has been mentioned in previous studies, but has not been quantified (see review [104,105]). Figure 2 summarizes the data of Table 2 (red squares for ECE pads, open green circles for NAO pads) with the addition of three studies that examined the impact of mass on brake emissions for a passenger car (grey triangles, [106]), and two vans (large squares with black borders [10] and blue borders [67] connected with dotted blue lines for better visualization). Only gray cast-iron discs data were used (i.e., coated discs or drum brakes were not considered). As expected, the dedicated studies show a linear correlation (see grey triangles), but the slope is not the same for all studies. However, when considering all brakes, the results of Table 2 indicate no correlation for ECE or NAO pads, because any correlation is masked from the material impact on the emissions. For all ECE pads the average correlation factor is 3.1 mg/km/brake per 1000 kg of vehicle mass (note the low R2 value).
Other researchers have suggested a non-linear (power) equation for the relation between brake emissions (mg/km/V) and vehicle mass (Wref in t) [94].
EF = b Wref(1/c),
where b (mg/km/V) and c (−) are constants. The constants for ECE pads of the data of Figure 2 were b = 12.7 and c = 1.87; values close to the urban emission factors of that study [94].
Table 9 gives the estimated emission factors per brake corner based on Table 2 or the correlation in Figure 2 for PM10 and based on Figure A1 and Figure A2 in the Appendix A for PM2.5 and PN, respectively.
The average mass of all vehicles using ECE pads (with GCI discs), was 1902 kg, of all passenger cars 1752 kg, and of all LCVs 2838 kg. The mass of 1525 kg is the average mass in running order of passenger cars from 2020 plus half more passenger as defined in GTR 24 for testing [107], 1760 kg is the starting mass of N1 vehicles class III, while 2250 is the mass of N1-III vehicles with 28% payload. From Table 2, the average mass of all cars tested with NAO pads was 1807 kg, with CC and HMC discs 2152 kg and with drum brakes 1844 kg.

4.2. Comparison with International Organization of Motor Vehicle Manufacturers (OICA) Data

At the end of 2021, the OICA presented a large number of emission factors measured by its members [108]. The dataset included all typical brakes in use at that time, from small cars to SUVs and light commercial vehicles. The emission factors, expressed per vehicle, were transformed per brake by dividing by 3. Figure 3 presents the results as a function of vehicle mass. As with the previous data, there is no correlation between brake emission factors and vehicle mass when all brakes are considered and not the same material is used. The mean emission factor of the OICA dataset was 6.8 mg/km/brake, with a mean vehicle mass of 2200 kg. Separately, the LCVs had 5.7 mg/km/brake (mass 2465 kg). Forcing a linear trendline, the correlation factor would be 3 mg/km/brake per 1000 kg of vehicle mass, almost identical with the finding of Table 2 for ECE brakes (3.1 mg/km/brake per 1000 kg of vehicle mass). The data from Table 2 are also plotted for completeness. There is a high similarity in the scatter of the points, mainly with the ECE data, probably because the majority of brakes in Europe are ECE. The 62 cases in Table 2 and the 35 from OICA stress with high confidence the representativity of the reported emission factors in this paper.

4.3. Brake Emission Factors at Vehicle Level

Based on the emission factors per brake corner (Table 9), and multiplying them by 2.83, Table 10 presents the emission factors per vehicle for ECE pads. For vehicle masses between 1525 and 2250 kg the PM10 emissions are 13.4–19.7 mg/km/vehicle. Vehicles with ECE pads at the front wheels and drum brakes at the rear have PM10 emission levels between 12.2 (1760 kg) and 15.3 (2250 kg) mg/km/V. PM10 emission factors with NAO pads assuming that the emissions per brake corner are independent from the vehicle mass are 4.7 mg/km/V, while with the mass dependency of Figure 2, they are 5.4–7.9 mg/km/V. A last scenario with advanced discs at the front brakes and NAO pads at the rear brakes gives a PM10 of 6.9 mg/km/V for all vehicle masses. The 2020 fleet emission factors are only slightly lower compared to the scenario with a fleet without regenerative braking, due to the small share of electrified vehicles.
To put the estimations into perspective, the fleet emission factors can be compared with field studies and emission inventories.

4.4. Roadside and Tunnel Studies

Table 11 summarizes the brake emission factors from roadside and tunnel studies using metals as tracers to the source (brakes). Studies that calculated brake emissions using traffic data and emission factors given in databases (e.g., EMEP/CORINAIR [109]) were not included in the table. The overall average PM10, considering the studies from 2004 on, is 5.9 mg/km/V. The average of the European studies gives 6.6 mg/km/V PM10 emissions. The values are much lower, almost half, compared to the emission factors estimated from measurements in the laboratories (Table 10).
The reasons for this discrepancy need to be better understood. It is possible that the contribution of brake particles at the roadside measurements is lower due to fewer braking events. It could be that the laboratory method does not accurately capture the deposition of brake particles on the wheels. An experimental study found that around 10% of the brake wear mass deposited on the wheel. This percentage depends on many factors, such as the rim design, the brake disc ventilation, the trip characteristics and the braking events and the environmental conditions [119]. Simulations showed that, in terms of number concentration, the deposition is >30% up to 20 μm. This assumption needs to be investigated.

4.5. Emission Inventories

Table 12 summarizes the brake emission factors for PM10 and PM2.5 of light-duty vehicles based on national emission inventories. The emission factors and methodology described in the European Monitoring and Evaluation Programme with European Environmental Agency (EMEP/EEA) Emissions Inventory Guidebook align with COPERT (Computer Programme to Estimate Emissions from Road Transport), the EU standard vehicle emissions calculator, widely utilized by most European countries for their inventories. The EMEP/EEA Emissions Inventory Guidebook [9] provides speed-dependent emission factors for estimating emissions from tire wear, brake wear and road abrasion. PM10 emission factors from the brake wear of passenger cars in COPERT range from 3.3 (BEV) to 12 mg/km (ICE). Correction factors are provided to account for different average speeds for mileages driven on urban, rural and highway roads, as brake wear decreases with increasing mean trip speed. This is because braking occurs more frequently in urban driving compared to highway driving, resulting in more brake wear [9,32]. Some European countries employ their own models to calculate emission inventories, like the UK, Netherlands, Denmark, and Sweden. However, in the context of non-exhaust emissions, almost all of them rely on the emission factors provided by the EMEP/EEA Emissions Inventory Guidebook. In the USA, brake wear emissions for passenger cars and vans are quoted as 13.8 and 15.3 mg/km, respectively, by the US EPA MOVES (Motor Vehicle Emission Simulator Tool) [120]. Lower values for brake wear emission factors are suggested by CARB’s EMFAC 2021 emissions model for California [121]. Regarding Australia, COPERT Australia is used to calculate the vehicle emission inventories, which is a special edition of COPERT designed to address the Australian fleet and driving conditions [95].

4.6. Total vs. Solid Particles

The emission factors presented refer to solid particles only (i.e., they do not evaporate at 350 °C) or, in a few cases, total particles, but without a separate nucleation mode. A volatile nucleation mode has been reported many times in the literature, when the temperature at the brake exceeds a critical temperature, typically in the range of 165 and 240 °C (see studies in [80] and discussion in [125]). This was already reported in 2000 [44] and confirmed by recent studies [52,71,103]. The increase of emissions can be orders of magnitude higher and it depends on the local super-saturation ratios. More studies are needed in this direction to confirm the reproducibility of the results, and most importantly, more studies are needed with the GTR 24 protocol. For this reason, no emission factors are presented for brakes exceeding their critical temperature.

5. Conclusions

In this study, we summarized brake wear emission factors from the literature. Approximately 30 studies were found in which non-standardized protocols were followed. Emission inventories are based partly on these studies. Another 62 additional emission factors were found in studies that followed the GTR 24 methodology, even if they were not fully compliant. The results were in good agreement with approximately 35 emission factors presented by OICA. The averages of these studies were compared with roadside measurements and emission inventories. Furthermore, the reduction potential of non-asbestos organic (NAO) pads, advanced discs, brake dust filters, and regenerative braking was calculated. The key findings are:
  • The airborne and/or PM10 fraction to total wear is 40–45% on average.
  • The PM2.5 to PM10 ratio is in the order of 40–45%.
  • ECE (i.e., low metal and semi metallic) pads with gray cast iron (GCI) discs emit on average around 3 mg/km/brake per 1000 kg of vehicle mass. However, there is a large variability and the exact value depends on the brake and/or disc combination. The emission factor at vehicle level is around 2.83 to 3 times higher.
  • NAO pads can reduce the emissions by at least 60%.
  • Advanced discs (coated GCI or carbon ceramic) can reduce the emissions by 60–80%. This may be further enhanced when appropriate pads are applied.
  • Brake dust filter can reduce the emission from around 50% (passive systems) to 75% (active systems).
  • The electrification of vehicles can reduce the emissions up to 60–80% due to regenerative braking. Lower reductions are observed with lower electrification levels.
  • Roadside measurements of brake emissions estimate lower emission factors than those estimated in this review paper.
  • The emission inventories are in quite good agreement with the emission factors of this review.
These conclusions should be considered a first approximation of the status of the market at the time of writing this paper. As the procedure has been standardized with GTR 24 since 2023, more accurate emission factors are expected in the future. Furthermore, the database is expected to get larger as the manufacturers will start type-approving their brakes in order to fulfil the upcoming Euro 7 regulation.

Author Contributions

Conceptualization, P.D., Z.S. and L.N.; formal analysis, B.G., T.G. and T.K; writing—original draft preparation, B.G.; writing—review and editing, T.G., P.D., T.K., L.N. and Z.S. All authors have read and agreed to the published version of the manuscript.

Funding

This research received no external funding.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Data sharing not applicable. No new data were created or analyzed in this study.

Conflicts of Interest

The authors declare no conflict of interest. The information and views set out are those of the authors and do not necessarily reflect the official opinion of the European Commission and/or their universities and companies. Neither the European Union institutions and bodies nor any person acting on their behalf may be held responsible for the use which may be made of the information contained therein. Mention of trade or commercial products does not constitute endorsement or recommendation by the authors or the European Commission.

Appendix A

Figure A1 and Figure A2 present the correlation of ECE and NAO pads with vehicle mass for PM2.5 and PN, respectively.
Atmosphere 15 00097 g0a1
Figure A1. PM2.5 emissions in function of vehicle mass for ECE (squares) and NAO (circles) pads and gray cast iron discs. Bigger squares with border are two dedicated studies that modified the vehicle mass and the dashed lines show their trendline assuming linear correlation for each study. The dotted line is the correlation line of the ECE and NAO brakes of Table 2.
Figure A1. PM2.5 emissions in function of vehicle mass for ECE (squares) and NAO (circles) pads and gray cast iron discs. Bigger squares with border are two dedicated studies that modified the vehicle mass and the dashed lines show their trendline assuming linear correlation for each study. The dotted line is the correlation line of the ECE and NAO brakes of Table 2.
Atmosphere 15 00097 g0a1
Atmosphere 15 00097 g0a2
Figure A2. PN emissions in function of vehicle mass for ECE (squares) and NAO (circles) pads and gray cast iron discs. Bigger squares with border are two dedicated studies that modified the vehicle mass and the dashed lines show their trendline assuming linear correlation for each study. The dotted line is the correlation line of the ECE and NAO brakes of Table 2.
Figure A2. PN emissions in function of vehicle mass for ECE (squares) and NAO (circles) pads and gray cast iron discs. Bigger squares with border are two dedicated studies that modified the vehicle mass and the dashed lines show their trendline assuming linear correlation for each study. The dotted line is the correlation line of the ECE and NAO brakes of Table 2.
Atmosphere 15 00097 g0a2

References

  1. Health Effects Institute. State of Global Air 2020; Health Effects Institute: Boston, MA, USA, 2020. [Google Scholar]
  2. Belis, C.A.; Karagulian, F.; Larsen, B.R.; Hopke, P.K. Critical Review and Meta-Analysis of Ambient Particulate Matter Source Apportionment Using Receptor Models in Europe. Atmos. Environ. 2013, 69, 94–108. [Google Scholar] [CrossRef]
  3. European Environment Agency. Air Quality in Europe: 2020 Report; Publications Office: Luxembourg, 2020. [Google Scholar]
  4. European Commission. Directorate General for Internal Market, Industry, Entrepreneurship and SMEs. In Euro 7 Impact Assessment Study; Publications Office: Luxembourg, 2022. [Google Scholar]
  5. EEA National Emissions Reported to the Convention on Long-Range Transboundary Air Pollution (LRTAP Convention). Available online: https://www.eea.europa.eu/en/datahub/datahubitem-view/5be6cebc-ed2b-4496-be59-93736fc4ad78?activeaccordion=2023 (accessed on 7 January 2024).
  6. EEA EIONET Central Data Repository, 2023. Available online: https://cdr.eionet.europa.eu/ (accessed on 7 January 2024).
  7. Air Quality Expert Group (AQEG) Non-Exhaust Emissions from Road Traffic. UK, 2019. Available online: https://uk-air.defra.gov.uk/assets/documents/reports/cat09/1907101151_20190709_Non_Exhaust_Emissions_typeset_Final.pdf (accessed on 7 January 2024).
  8. Fussell, J.C.; Franklin, M.; Green, D.C.; Gustafsson, M.; Harrison, R.M.; Hicks, W.; Kelly, F.J.; Kishta, F.; Miller, M.R.; Mudway, I.S.; et al. A Review of Road Traffic-Derived Non-Exhaust Particles: Emissions, Physicochemical Characteristics, Health Risks, and Mitigation Measures. Environ. Sci. Technol. 2022, 56, 6813–6835. [Google Scholar] [CrossRef]
  9. EMEP/EEA. EMEP/EEA Air Pollutant Emission Inventory Guidebook 2019 1.A.3.b.vi-Vii Road Tyre and Brake Wear 2019. 2009. Available online: https://www.eea.europa.eu/publications/emep-eea-guidebook-2019/part-b-sectoral-guidance-chapters/1-energy/1-a-combustion/1-a-3-b-vi/view (accessed on 7 January 2024).
  10. Grigoratos, T.; Mathissen, M.; Vedula, R.; Mamakos, A.; Agudelo, C.; Gramstat, S.; Giechaskiel, B. Interlaboratory Study on Brake Particle Emissions—Part I: Particulate Matter Mass Emissions. Atmosphere 2023, 14, 498. [Google Scholar] [CrossRef]
  11. Aranke, O.; Algenaid, W.; Awe, S.; Joshi, S. Coatings for Automotive Gray Cast Iron Brake Discs: A Review. Coatings 2019, 9, 552. [Google Scholar] [CrossRef]
  12. Mulani, S.M.; Kumar, A.; Shaikh, H.N.E.A.; Saurabh, A.; Singh, P.K.; Verma, P.C. A Review on Recent Development and Challenges in Automotive Brake Pad-Disc System. Mater. Today: Proc. 2022, 56, 447–454. [Google Scholar] [CrossRef]
  13. Ghouri, I.; Barker, R.; Brooks, P.; Kosarieh, S.; Barton, D. The Effects of Corrosion on Particle Emissions from a Grey Cast Iron Brake Disc; 2022-01–1178; SAE International: Warrendale, PA, USA.
  14. Perricone, G.; Matějka, V.; Alemani, M.; Valota, G.; Bonfanti, A.; Ciotti, A.; Olofsson, U.; Söderberg, A.; Wahlström, J.; Nosko, O.; et al. A Concept for Reducing PM 10 Emissions for Car Brakes by 50%. Wear 2018, 396–397, 135–145. [Google Scholar] [CrossRef]
  15. Vasiljević, S.; Glišović, J.; Stojanović, B.; Vencl, A. Review of the Coatings Used for Brake Discs Regarding Their Wear Resistance and Environmental Effect. Proc. Inst. Mech. Eng. Part J J. Eng. Tribol. 2022, 236, 1932–1949. [Google Scholar] [CrossRef]
  16. Seo, H.; Park, J.; Kim, Y.C.; Lee, J.J.; Jang, H. Effect of Disc Materials on Brake Emission during Moderate-Temperature Braking. Tribol. Int. 2021, 163, 107185. [Google Scholar] [CrossRef]
  17. Dizdar, S.; Lyu, Y.; Lampa, C.; Olofsson, U. Grey Cast Iron Brake Discs Laser Cladded with Nickel-Tungsten Carbide—Friction, Wear and Airborne Wear Particle Emission. Atmosphere 2020, 11, 621. [Google Scholar] [CrossRef]
  18. Güney, B.; Mutlu, I. Tribological Properties of Brake Discs Coated with Cr2O3—40% Tio2 by Plasma Spraying. Surf. Rev. Lett. 2019, 26, 1950075. [Google Scholar] [CrossRef]
  19. Holzgaßner, L.; Singh, R.; Bernhardt, S. Particle Emission Reduction for Brake Discs via High-Performance Cold Spray Coating. Presented at the Chassis; Tech Plus: Munich, Germany, 2023. [Google Scholar]
  20. Day, A.; Bryant, D. Braking of Road Vehicles, 2nd ed.; Butterworth-Heinemann: Kidlington, UK; Cambridge, MA, USA, 2022; ISBN 978-0-12-822005-4. [Google Scholar]
  21. Borawski, A. Conventional and Unconventional Materials Used in the Production of Brake Pads—Review. Sci. Eng. Compos. Mater. 2020, 27, 374–396. [Google Scholar] [CrossRef]
  22. Sinha, A.; Ischia, G.; Menapace, C.; Gialanella, S. Experimental Characterization Protocols for Wear Products from Disc Brake Materials. Atmosphere 2020, 11, 1102. [Google Scholar] [CrossRef]
  23. Woo, S.-H.; Kim, Y.; Lee, S.; Choi, Y.; Lee, S. Characteristics of Brake Wear Particle (BWP) Emissions under Various Test Driving Cycles. Wear 2021, 480–481, 203936. [Google Scholar] [CrossRef]
  24. Wahlström, J.; Söderberg, A.; Olander, L.; Jansson, A.; Olofsson, U. A Pin-on-Disc Simulation of Airborne Wear Particles from Disc Brakes. Wear 2010, 268, 763–769. [Google Scholar] [CrossRef]
  25. Woo, S.-H.; Jang, H.; Na, M.Y.; Chang, H.J.; Lee, S. Characterization of Brake Particles Emitted from Non-Asbestos Organic and Low-Metallic Brake Pads under Normal and Harsh Braking Conditions. Atmos. Environ. 2022, 278, 119089. [Google Scholar] [CrossRef]
  26. Reich, A.; Sarda, A.; Semsch, M. Drag Torque in Disk Brakes: Significance, Measurement and Challenges. SAE Int. J. Commer. Veh. 2015, 8, 276–282. [Google Scholar] [CrossRef]
  27. Danner, C.; Pein, A. Preview on Future Developments of Non-Exhaust Emissions. In 12th International Munich Chassis Symposium 2021; Pfeffer, P., Ed.; Proceedings; Springer: Berlin/Heidelberg, Germany, 2022; pp. 497–513. ISBN 978-3-662-64549-9. [Google Scholar]
  28. Storch, L.; Hamatschek, C.; Hesse, D.; Feist, F.; Bachmann, T.; Eichler, P.; Grigoratos, T. Comprehensive Analysis of Current Primary Measures to Mitigate Brake Wear Particle Emissions from Light-Duty Vehicles. Atmosphere 2023, 14, 712. [Google Scholar] [CrossRef]
  29. Cha, S.; Carter, P.; Bradow, R.L. Simulation of Automobile Brake Wear Dynamics and Estimation of Emissions; 831036; SAE: Warrendale, PA, USA, 1983. [Google Scholar]
  30. Tutuianu, M.; Bonnel, P.; Ciuffo, B.; Haniu, T.; Ichikawa, N.; Marotta, A.; Pavlovic, J.; Steven, H. Development of the World-Wide Harmonized Light Duty Test Cycle (WLTC) and a Possible Pathway for Its Introduction in the European Legislation. Transp. Res. Part D Transp. Environ. 2015, 40, 61–75. [Google Scholar] [CrossRef]
  31. Mathissen, M.; Grochowicz, J.; Schmidt, C.; Vogt, R.; Farwick zum Hagen, F.H.; Grabiec, T.; Steven, H.; Grigoratos, T. A Novel Real-World Braking Cycle for Studying Brake Wear Particle Emissions. Wear 2018, 414–415, 219–226. [Google Scholar] [CrossRef]
  32. Luhana, L.; Sokhi, R.S.; Warner, L.; Mao, H.; Boulter, P.; McCrae, I.; Wright, J.; Osborn, D. Measurement of Non-Exhaust Particulate Matter; Deliverable to Particulates project; TRL: Berkshire, UK, 2004. [Google Scholar]
  33. Grigoratos, T.; Martini, G. Brake Wear Particle Emissions: A Review. Environ. Sci. Pollut. Res. 2015, 22, 2491–2504. [Google Scholar] [CrossRef]
  34. Kukutschová, J.; Filip, P. Review of Brake Wear Emissions. In Non-Exhaust Emissions; Academic Press: London, UK, 2018; pp. 123–146. ISBN 978-0-12-811770-5. [Google Scholar]
  35. Wahid, S.M.S. Automotive Brake Wear: A Review. Environ. Sci Pollut Res 2018, 25, 174–180. [Google Scholar] [CrossRef]
  36. Perricone, G.; Alemani, M.; Wahlström, J.; Olofsson, U. A Proposed Driving Cycle for Brake Emissions Investigation for Test Stand. Proc. Inst. Mech. Eng. Part D J. Automob. Eng. 2020, 234, 122–135. [Google Scholar] [CrossRef]
  37. Semadeni-Davies, A.; Coulson, G.; Gadd, J.; Somervell, E.; Longely, I.; Olivares, G. Determining the Ecological and Air Quality Impacts of Particulate Matter from Brake and Tyre Wear and Road Surface Dust: Stage 1, Literature Review and Recommendations for Developing New Emission Factors for New Zealand; Waka Kotahi, N.Z., Ed.; Transport Agency: Wellington, New Zealand, 2021; ISBN 978-1-990044-37-3. [Google Scholar]
  38. Guo, D.; Wei, H.; Guo, Y.; Wang, C.; Yin, Z. Non-Exhaust Particulate Matter Emission from Vehicles: A Review. E3S Web Conf. 2021, 268, 01015. [Google Scholar] [CrossRef]
  39. Rahimi, M.; Bortoluzzi, D.; Wahlström, J. Input Parameters for Airborne Brake Wear Emission Simulations: A Comprehensive Review. Atmosphere 2021, 12, 871. [Google Scholar] [CrossRef]
  40. Piscitello, A.; Bianco, C.; Casasso, A.; Sethi, R. Non-Exhaust Traffic Emissions: Sources, Characterization, and Mitigation Measures. Sci. Total Environ. 2021, 766, 144440. [Google Scholar] [CrossRef]
  41. Liu, Y.; Wu, S.; Chen, H.; Federici, M.; Perricone, G.; Li, Y.; Lv, G.; Munir, S.; Luo, Z.; Mao, B. Brake Wear Induced PM10 Emissions during the World Harmonised Light-Duty Vehicle Test Procedure-Brake Cycle. J. Clean. Prod. 2022, 361, 132278. [Google Scholar] [CrossRef]
  42. Wang, Y.; Yin, H.; Yang, Z.; Su, S.; Hao, L.; Tan, J.; Wang, X.; Niu, Z.; Ge, Y. Assessing the Brake Particle Emissions for Sustainable Transport: A Review. Renew. Sustain. Energy Rev. 2022, 167, 112737. [Google Scholar] [CrossRef]
  43. Feo, M.L.; Torre, M.; Tratzi, P.; Battistelli, F.; Tomassetti, L.; Petracchini, F.; Guerriero, E.; Paolini, V. Laboratory and On-Road Testing for Brake Wear Particle Emissions: A Review. Environ. Sci. Pollut. Res. 2023, 30, 100282–100300. [Google Scholar] [CrossRef]
  44. Garg, B.D.; Cadle, S.H.; Mulawa, P.A.; Groblicki, P.J.; Laroo, C.; Parr, G.A. Brake Wear Particulate Matter Emissions. Environ. Sci. Technol. 2000, 34, 4463–4469. [Google Scholar] [CrossRef]
  45. Westerlund, K.-G.; Johansson, C. Emissions of Metals and Particulate Matter Due to Wear of Brake Linings in Stockholm. In Air Pollution X; Brebbia, C.A., Martin-Duque, J.F., Eds.; WIT Press: Southampton, UK, 2002; ISBN 1-85312-916-X. [Google Scholar]
  46. Sanders, P.G.; Xu, N.; Dalka, T.M.; Maricq, M.M. Airborne Brake Wear Debris: Size Distributions, Composition, and a Comparison of Dynamometer and Vehicle Tests. Environ. Sci. Technol. 2003, 37, 4060–4069. [Google Scholar] [CrossRef]
  47. Iijima, A.; Sato, K.; Yano, K.; Kato, M.; Kozawa, K.; Furuta, N. Emission Factor for Antimony in Brake Abrasion Dusts as One of the Major Atmospheric Antimony Sources. Environ. Sci. Technol. 2008, 42, 2937–2942. [Google Scholar] [CrossRef]
  48. Hagino, H.; Oyama, M.; Sasaki, S. Airborne Brake Wear Particle Emission Due to Braking and Accelerating. Wear 2015, 334–335, 44–48. [Google Scholar] [CrossRef]
  49. Hagino, H.; Oyama, M.; Sasaki, S. Laboratory Testing of Airborne Brake Wear Particle Emissions Using a Dynamometer System under Urban City Driving Cycles. Atmos. Environ. 2016, 131, 269–278. [Google Scholar] [CrossRef]
  50. Perricone, G.; Alemani, M.; Metinöz, I.; Matějka, V.; Wahlström, J.; Olofsson, U. Towards the Ranking of Airborne Particle Emissions from Car Brakes—A System Approach. Proc. Inst. Mech. Eng. Part D J. Automob. Eng. 2017, 231, 781–797. [Google Scholar] [CrossRef]
  51. Farwick zum Hagen, F.H.; Mathissen, M.; Grabiec, T.; Hennicke, T.; Rettig, M.; Grochowicz, J.; Vogt, R.; Benter, T. On-Road Vehicle Measurements of Brake Wear Particle Emissions. Atmos. Environ. 2019, 217, 116943. [Google Scholar] [CrossRef]
  52. Mathissen, M.; Grigoratos, T.; Lahde, T.; Vogt, R. Brake Wear Particle Emissions of a Passenger Car Measured on a Chassis Dynamometer. Atmosphere 2019, 10, 556. [Google Scholar] [CrossRef]
  53. Hesse, D.; Augsburg, K. Real Driving Emissions Measurement of Brake Dust Particles; 2019-01–2138; SAE: Warrendale, PA, USA, 2019. [Google Scholar]
  54. Vojtíšek-Lom, M.; Vaculík, M.; Pechout, M.; Hopan, F.; Arul Raj, A.F.; Penumarti, S.; Horák, J.S.; Popovicheva, O.; Ondráček, J.; Doušová, B. Effects of Braking Conditions on Nanoparticle Emissions from Passenger Car Friction Brakes. Sci. Total Environ. 2021, 788, 147779. [Google Scholar] [CrossRef]
  55. Kim, S.-H.; Shim, W.; Kwon, S.-U.; Lee, J.-J.; Seo, M.-W.; Kim, J.-K.; Pee, J.-H.; Kim, J.-Y. The Impact of Composition in Non-Steel and Low-Steel Type Friction Materials on Airborne Brake Wear Particulate Emission. Tribol. Lett. 2020, 68, 118. [Google Scholar] [CrossRef]
  56. Park, J.; Joo, B.; Seo, H.; Song, W.; Lee, J.J.; Lee, W.K.; Jang, H. Analysis of Wear Induced Particle Emissions from Brake Pads during the Worldwide Harmonized Light Vehicles Test Procedure (WLTP). Wear 2021, 466–467, 203539. [Google Scholar] [CrossRef]
  57. Kim, S.-H.; Jeong, M.H.; Kim, J.; Shim, W.; Kwon, S.-U.; Lee, J.-J.; Huh, S.H.; Pee, J.-H.; Kim, J.-Y. Dynamometric Investigation on Airborne Particulate Matter (PM) from Friction Materials for Automobile: Impact of Abrasive and Lubricant on PM Emission Factor. Lubricants 2021, 9, 118. [Google Scholar] [CrossRef]
  58. Woo, S.-H.; Jang, H.; Lee, S.-B.; Lee, S. Comparison of Total PM Emissions Emitted from Electric and Internal Combustion Engine Vehicles: An Experimental Analysis. Sci. Total Environ. 2022, 842, 156961. [Google Scholar] [CrossRef]
  59. Andersson, J.; Campbell, M.; Marshall, I.; Kramer, L.; Norris, J. Measurement of Emissions from Brake and Tyre Wear. Final Report—Phase 1; Ricardo: Shoreham-by-Sea, UK, 2022. [Google Scholar]
  60. Huber, M.P.; Murg, J.; Fischer, P. Assessing a Vehicle’s Real-World Brake Wear Particle Emissions on Public Roads. In Proceedings of the EuroBrake 2023, EB2023-TST-002, Barcelona, Spain, 12–14 September 2023. [Google Scholar]
  61. Zhang, Q.; Fang, T.; Men, Z.; Wei, N.; Peng, J.; Du, T.; Zhang, X.; Ma, Y.; Wu, L.; Mao, H. Direct Measurement of Brake and Tire Wear Particles Based on Real-World Driving Conditions. Sci. Total Environ. 2024, 906, 167764. [Google Scholar] [CrossRef]
  62. zum Hagen, F.H.F.; Mathissen, M.; Grabiec, T.; Hennicke, T.; Rettig, M.; Grochowicz, J.; Vogt, R.; Benter, T. Study of Brake Wear Particle Emissions: Impact of Braking and Cruising Conditions. Environ. Sci. Technol. 2019, 53, 5143–5150. [Google Scholar] [CrossRef]
  63. Mamakos, A.; Arndt, M.; Hesse, D.; Augsburg, K. Physical Characterization of Brake-Wear Particles in a PM10 Dilution Tunnel. Atmosphere 2019, 10, 639. [Google Scholar] [CrossRef]
  64. Hagino, H. Sensitivity and Reproducibility of Brake Wear Particle Emission Measurements Using JARI System. In Proceedings of the 50th PMP Meeting, Brussels, Belgium, 3–4 April 2019. [Google Scholar]
  65. Mamakos, A.; Arndt, M.; Hesse, D.; Hamatschek, C.; Augsburg, K. Comparison of Particulate Matter and Number Emissions from a Floating and a Fixed Caliper Brake System of the Same Lining Formulation; 2020-01–1633; SAE: Warrendale, PA, USA, 2020. [Google Scholar]
  66. Mamakos, A.; Huber, M.P.; Arndt, M.; Reingruber, H.; Steiner, G.; Weidinger, C. Design of a Laboratory Sampling System for Brake Wear Particle Measurements; 2022-01–1179; SAE: Warrendale, PA, USA, 2022. [Google Scholar]
  67. Agudelo, C.; Vedula, R.T.; Collier, S.; Stanard, A. Brake Particulate Matter Emissions Measurements for Six Light-Duty Vehicles Using Inertia Dynamometer Testing; 2020-01–1637; SAE: Warrendale, PA, USA, 2020. [Google Scholar]
  68. Gramstat, S.; Mertens, T.; Waninger, R.; Lugovyy, D. Impacts on Brake Particle Emission Testing. Atmosphere 2020, 11, 1132. [Google Scholar] [CrossRef]
  69. Gramstat, S.; Mertens, T.; Waninger, R.; Augsburg, K.; Hamatschek, C.; Hesse, D. Functional Coatings of Gray-Cast Iron Brake Discs—Impact on the Tribology. In Berichte aus dem µ-Club 2020; Mayer, R., Ed.; Springer: Berlin/Heidelberg, Germany, 2021; pp. 162–170. ISBN 978-3-662-63027-3. [Google Scholar]
  70. Hamatschek, C.; Augsburg, K.; Schobel, D.; Gramstat, S.; Stich, A.; Gulden, F.; Hesse, D. Comparative Study on the Friction Behaviour and the Particle Formation Process between a Laser Cladded Brake Disc and a Conventional Grey Cast Iron Disc. Metals 2023, 13, 300. [Google Scholar] [CrossRef]
  71. Hesse, D.; Hamatschek, C.; Augsburg, K.; Weigelt, T.; Prahst, A.; Gramstat, S. Testing of Alternative Disc Brakes and Friction Materials Regarding Brake Wear Particle Emissions and Temperature Behavior. Atmosphere 2021, 12, 436. [Google Scholar] [CrossRef]
  72. Huber, M.P.; Fischer, P.; Mamakos, A.; Steiner, G.; Klug, A. Measuring Brake Wear Particles with a Real-Driving Emissions Sampling System on a Brake Dynamometer; 2022-01–1180; SAE: Warrendale, PA, USA, 2022. [Google Scholar]
  73. Mathissen, M.; Grigoratos, T.; Gramstat, S.; Mamakos, A.; Vedula, R.; Agudelo, C.; Grochowicz, J.; Giechaskiel, B. Interlaboratory Study on Brake Particle Emissions Part II: Particle Number Emissions. Atmosphere 2023, 14, 424. [Google Scholar] [CrossRef]
  74. Hagino, H. Brake Wear Particle Emission Measurements Based on Real Driving Cycles in Several Urban Areas in a Laboratory Testing; EB2023-TST-009. In Proceedings of the EuroBarakes 2023, Barcelona, Spain, 12–14 September 2023. [Google Scholar]
  75. Sin, A. Comparison of Different Tribological Couples Respect to Pm10 Emissions; EB2023-EFA-010. In Proceedings of the EuroBrake 2023, Barcelona, Spain, 12–14 September 2023. [Google Scholar]
  76. Adamczak, L. At Source Brake Dust Active Filtering System; EB2023-EFA-008. In Proceedings of the EuroBrake 2023, Barcelona, Spain, 12–14 September 2023. [Google Scholar]
  77. Hagino, H.; Iwata, A.; Okuda, T. Iron Oxide and Hydroxide Speciation in Emissions of Brake-Wear Particles from Different Friction Materials Using X-Ray Absorption Fine Structure. Atmosphere 2023, 15, 49. [Google Scholar] [CrossRef]
  78. Hagino, H. Investigation of Brake-Wear Particle Emissions from Regenerative-Friction Brake Coordination Systems via Dynamometer Testing. Atmosphere 2024, 15, 75. [Google Scholar] [CrossRef]
  79. Grigoratos, T.; Mamakos, A.; Vedula, R.; Arndt, M.; Lugovyy, D.; Hafenmayer, C.; Moisio, M.; Agudelo, C.; Giechaskiel, B. Characterization of Laboratory Particulate Matter (PM) Mass Setups for Brake Emission Measurements. Atmosphere 2023, 14, 516. [Google Scholar] [CrossRef]
  80. Stojanovic, N.; Abdullah, O.I.; Grujic, I.; Boskovic, B. Particles Formation Due to the Wear of Tires and Measures for the Wear Reduction: A Review. Proc. Inst. Mech. Eng. Part D J. Automob. Eng. 2022, 236, 3075–3089. [Google Scholar] [CrossRef]
  81. Candeo, S.; Leonardi, M.; Gialanella, S.; Straffelini, S. Influence of Contact Pressure and Velocity on the Brake Behaviour and Particulate Matter Emissions. Wear 2023, 514–515, 204579. [Google Scholar] [CrossRef]
  82. Steege, R.; Welp, D.; Lange, J. The Contribution of Brake Emissions to the Total Vehicle Emissions. In 6th International Munich Chassis Symposium 2015; Pfeffer, P., Ed.; Proceedings; Springer: Wiesbaden, Germany, 2015; pp. 585–603. ISBN 978-3-658-09710-3. [Google Scholar]
  83. Hamatschek, C.; Hesse, D.; Augsburg, K.; Gramstat, S.; Stich, A. Comparison of the Particle Emission Behaviour of Automotive Drum and Disc Brakes. In 12th International Munich Chassis Symposium 2021; Pfeffer, P., Ed.; Proceedings; Springer: Berlin/Heidelberg, Germany, 2022; pp. 541–563. ISBN 978-3-662-64549-9. [Google Scholar]
  84. Wahlström, J.; Lyu, Y.; Matjeka, V.; Söderberg, A. A Pin-on-Disc Tribometer Study of Disc Brake Contact Pairs with Respect to Wear and Airborne Particle Emissions. Wear 2017, 384–385, 124–130. [Google Scholar] [CrossRef]
  85. Kılıç, H.; Mısırlı, C. Investigation of Tribological Behavior of 20NiCrBSi-WC12Co Coated Brake Disc by HVOF Method. Mater. Res. Express 2020, 7, 016560. [Google Scholar] [CrossRef]
  86. Fieldhouse, J.D.; Gelb, J. New Developments of an On-Vehicle Brake Pad Waste Collection System. SAE Int. J. Passeng. Cars -Mech. Syst. 2016, 9, 1245–1254. [Google Scholar] [CrossRef]
  87. Hascoët, M.; Adamczak, L. At Source Brake Dust Collection System. Results Eng. 2020, 5, 100083. [Google Scholar] [CrossRef]
  88. Gramstat, S.; Hascoet, M.; Rocca-Serra, C.; Adamczak, L. Potentials and Challenges of a Brake Particle Emission Collecting System; 2020-01–1635; SAE: Warrendale, PA, USA, 2020. [Google Scholar]
  89. Hwang, I.S.; Lee, Y.L. A Study on the Pressure Drop Characteristics of a Passive Filter System for Collecting Fine Brake Dust. Int.J. Automot. Technol. 2021, 22, 1257–1265. [Google Scholar] [CrossRef]
  90. Hwang, I.S.; Park, J.-T.; Lee, Y.L. Feasibility of a Porous Ceramic Filter for Collecting Brake Fine Dust. Int.J. Automot. Technol. 2022, 23, 521–527. [Google Scholar] [CrossRef]
  91. Woo, S.-H.; Lee, G.; Han, B.; Lee, S. Development of Dust Collectors to Reduce Brake Wear PM Emissions. Atmosphere 2022, 13, 1121. [Google Scholar] [CrossRef]
  92. Keller, F.; Wörz, T.; Beck, A.; Kopriva, M.; Uhlir, M.; Pfannkuch, S. Development of an Active Brake Dust Particle Filter System to Reduce Brake Dust Emissions. EB2023-EFA-007. In Proceedings of the EuroBrake 2023, Barcelona, Spain, 12–14 September 2023. [Google Scholar]
  93. Timmers, V.R.J.H.; Achten, P.A.J. Non-Exhaust PM Emissions from Electric Vehicles. Atmos. Environ. 2016, 134, 10–17. [Google Scholar] [CrossRef]
  94. Beddows, D.C.S.; Harrison, R.M. PM10 and PM2.5 Emission Factors for Non-Exhaust Particles from Road Vehicles: Dependence upon Vehicle Mass and Implications for Battery Electric Vehicles. Atmos. Environ. 2021, 244, 117886. [Google Scholar] [CrossRef]
  95. Smit, R. Non-Exhaust PM Emissions from Battery Electric Vehicles (BEVs)—Does the Argument against Electric Vehicles Stack up? TER (Transport Energy/Emission Research Pty Ltd.): Australia, 2020. Available online: https://www.transport-e-research.com/_files/ugd/d0bd25_029571fc6c8a4d80a46adc23dd74ebfd.pdf (accessed on 7 January 2024).
  96. Liu, Y.; Chen, H.; Gao, J.; Li, Y.; Dave, K.; Chen, J.; Federici, M.; Perricone, G. Comparative Analysis of Non-Exhaust Airborne Particles from Electric and Internal Combustion Engine Vehicles. J. Hazard. Mater. 2021, 420, 126626. [Google Scholar] [CrossRef]
  97. Hooftman, N.; Oliveira, L.; Messagie, M.; Coosemans, T.; Van Mierlo, J. Environmental Analysis of Petrol, Diesel and Electric Passenger Cars in a Belgian Urban Setting. Energies 2016, 9, 84. [Google Scholar] [CrossRef]
  98. Jung, H. Fuel Economy of Plug-In Hybrid Electric and Hybrid Electric Vehicles: Effects of Vehicle Weight, Hybridization Ratio and Ambient Temperature. WEVJ 2020, 11, 31. [Google Scholar] [CrossRef]
  99. ACEA Making the Transition to Zero-Emission Mobility. 2022 Progress Report. Available online: https://www.acea.auto/publication/2022-progress-report-making-the-transition-to-zero-emission-mobility/ (accessed on 7 January 2024).
  100. Koupal, J.; DenBleyker, A.; Kishan, S.; Vedula, R.; Agudelo, C. Brake Wear Particulate Matter Emissions Modeling; Eastern Research Group: Boston, MA, USA, 2021. [Google Scholar]
  101. Dimopoulos Eggenschwiler, P.; Schreiber, D.; Habersatter, J. Brake Particle PN and PM Emissions of a Hybrid Light Duty Vehicle Measured on the Chassis Dynamometer. Atmosphere 2023, 14, 784. [Google Scholar] [CrossRef]
  102. Bondorf, L.; Köhler, L.; Grein, T.; Epple, F.; Philipps, F.; Aigner, M.; Schripp, T. Airborne Brake Wear Emissions from a Battery Electric Vehicle. Atmosphere 2023, 14, 488. [Google Scholar] [CrossRef]
  103. Men, Z.; Zhang, X.; Peng, J.; Zhang, J.; Fang, T.; Guo, Q.; Wei, N.; Zhang, Q.; Wang, T.; Wu, L.; et al. Determining Factors and Parameterization of Brake Wear Particle Emission. J. Hazard. Mater. 2022, 434, 128856. [Google Scholar] [CrossRef]
  104. Timmers, V.R.J.H.; Achten, P.A.J. Non-Exhaust PM Emissions from Battery Electric Vehicles. In Non-Exhaust Emissions; Elsevier: Amsterdam, The Netherlands, 2018; pp. 261–287. ISBN 978-0-12-811770-5. [Google Scholar]
  105. Maricq, M.M. Engine, Aftertreatment, Fuel Quality and Non-Tailpipe Achievements to Lower Gasoline Vehicle PM Emissions: Literature Review and Future Prospects. Sci. Total Environ. 2023, 866, 161225. [Google Scholar] [CrossRef]
  106. Kolbeck, K.; Schröder, T.; Schlichting, M.; Bacher, H. Evaluation of Different Influencing Parameters on the Result of Brake Particle Emission Measurements; EB2022-FBR-011. In Proceedings of the EuroBrake 2022, Online, 17–19 May 2022. [Google Scholar]
  107. European Commission; EEA Climate and Energy in the EU. Data. Country Comparison. 2023. Available online: https://climate-energy.eea.europa.eu/topics/transport/emissions-from-cars/data (accessed on 7 January 2024).
  108. OICA OICA Views on Brake Wear Particles. Presented at the PMP Webex, Online, 2021. Available online: https://wiki.unece.org/display/trans/pmp+web+conference+01.12.2021 (accessed on 7 January 2024).
  109. Thorpe, A.J.; Harrison, R.M.; Boulter, P.G.; McCrae, I.S. Estimation of Particle Resuspension Source Strength on a Major London Road. Atmos. Environ. 2007, 41, 8007–8020. [Google Scholar] [CrossRef]
  110. Abu-Allaban, M.; Gillies, J.A.; Gertler, A.W.; Clayton, R.; Proffitt, D. Tailpipe, Resuspended Road Dust, and Brake-Wear Emission Factors from on-Road Vehicles. Atmos. Environ. 2003, 37, 5283–5293. [Google Scholar] [CrossRef]
  111. Bukowiecki, N.; Lienemann, P.; Hill, M.; Furger, M.; Richard, A.; Amato, F.; Prévôt, A.S.H.; Baltensperger, U.; Buchmann, B.; Gehrig, R. PM10 Emission Factors for Non-Exhaust Particles Generated by Road Traffic in an Urban Street Canyon and along a Freeway in Switzerland. Atmos. Environ. 2010, 44, 2330–2340. [Google Scholar] [CrossRef]
  112. Amato, F.; Favez, O.; Pandolfi, M.; Alastuey, A.; Querol, X.; Moukhtar, S.; Bruge, B.; Verlhac, S.; Orza, J.A.G.; Bonnaire, N.; et al. Traffic Induced Particle Resuspension in Paris: Emission Factors and Source Contributions. Atmos. Environ. 2016, 129, 114–124. [Google Scholar] [CrossRef]
  113. Lawrence, S.; Sokhi, R.; Ravindra, K. Quantification of Vehicle Fleet PM 10 Particulate Matter Emission Factors from Exhaust and Non-Exhaust Sources Using Tunnel Measurement Techniques. Environ. Pollut. 2016, 210, 419–428. [Google Scholar] [CrossRef]
  114. Charron, A.; Polo-Rehn, L.; Besombes, J.-L.; Golly, B.; Buisson, C.; Chanut, H.; Marchand, N.; Guillaud, G.; Jaffrezo, J.-L. Identification and Quantification of Particulate Tracers of Exhaust and Non-Exhaust Vehicle Emissions. Atmos. Chem. Phys. 2019, 19, 5187–5207. [Google Scholar] [CrossRef]
  115. Zhang, J.; Peng, J.; Song, C.; Ma, C.; Men, Z.; Wu, J.; Wu, L.; Wang, T.; Zhang, X.; Tao, S.; et al. Vehicular Non-Exhaust Particulate Emissions in Chinese Megacities: Source Profiles, Real-World Emission Factors, and Inventories. Environ. Pollut. 2020, 266, 115268. [Google Scholar] [CrossRef]
  116. Hicks, W.; Beevers, S.; Tremper, A.H.; Stewart, G.; Priestman, M.; Kelly, F.J.; Lanoisellé, M.; Lowry, D.; Green, D.C. Quantification of Non-Exhaust Particulate Matter Traffic Emissions and the Impact of COVID-19 Lockdown at London Marylebone Road. Atmosphere 2021, 12, 190. [Google Scholar] [CrossRef]
  117. Beddows, D.C.S.; Harrison, R.M.; Gonet, T.; Maher, B.A.; Odling, N. Measurement of Road Traffic Brake and Tyre Dust Emissions Using Both Particle Composition and Size Distribution Data. Environ. Pollut. 2023, 331, 121830. [Google Scholar] [CrossRef]
  118. Liu, J.; Peng, J.; Men, Z.; Fang, T.; Zhang, J.; Du, Z.; Zhang, Q.; Wang, T.; Wu, L.; Mao, H. Brake Wear-Derived Particles: Single-Particle Mass Spectral Signatures and Real-World Emissions. Environ. Sci. Ecotechnology 2023, 15, 100240. [Google Scholar] [CrossRef]
  119. Hesse, D.; Hamatschek, C.; Feißel, T.; Sachse, H.; Augsburg, K.; Gramstat, S. Investigations on the Deposition Behaviour of Brake Wear Particles on the Wheel Surface; 2021-01–1301; SAE: Warrendale, PA, USA, 2021. [Google Scholar]
  120. EPA. Brake and Tire Wear Emissions from Onroad Vehicles in MOVES3. Report EPA-420-R-20-014, 2020. Available online: https://www.epa.gov/sites/default/files/2020-11/documents/420r20014.pdf (accessed on 7 January 2024).
  121. Agudelo, C. California Air Resources Board (CARB) Updates to Brake EMissions FACtors (EMFAC) Using Dynamometer Tests for Light-Duty Vehicles. In Proceedings of the 26th ETH Nanoparticles Conference, Zurich, Switzerland, 20–22 June 2023. [Google Scholar]
  122. NAEI Fleet Weighted Road Transport Emission Factors 2020. Available online: https://naei.beis.gov.uk/data/ef-transport (accessed on 7 January 2024).
  123. DCE—Danish Centre for Environment and Energy Non-Exhaust Emission Factors. Available online: https://envs.au.dk/fileadmin/envs/Emission_inventories/Emission_factors/Emf_internet__Non-ex-PM-HM.htm (accessed on 7 January 2024).
  124. PBL—Netherlands Environmental Assessment Agency Methods for Calculating the Emissions of Transport in the Netherlands. 2021. Available online: https://www.pbl.nl/en/publications/methods-for-calculating-the-emissions-of-transport-in-the-netherlands-2021 (accessed on 7 January 2024).
  125. Vasiljević, S.; Glišović, J.; Lukić, J.; Miloradović, D.; Stanojević, M.; Đorđević, M. Analysis of Parameters Influencing the Formation of Particles during the Braking Process: Experimental Approach. Atmosphere 2023, 14, 1618. [Google Scholar] [CrossRef]
Atmosphere 15 00097 g001
Figure 1. Evolution and projections of exhaust, non-exhaust (brake, tire, and road wear), and total PM emissions from road transport in EU27 [4]: (a) PM10; (b) PM2.5. Percentages give contribution of non-exhaust to total PM at years 2010, 2020, 2030, 2040 and 2050. The decrease of emissions in 2020 was due to the COVID-19 restrictions.
Figure 1. Evolution and projections of exhaust, non-exhaust (brake, tire, and road wear), and total PM emissions from road transport in EU27 [4]: (a) PM10; (b) PM2.5. Percentages give contribution of non-exhaust to total PM at years 2010, 2020, 2030, 2040 and 2050. The decrease of emissions in 2020 was due to the COVID-19 restrictions.
Atmosphere 15 00097 g001
Atmosphere 15 00097 g002
Figure 2. PM10 emissions in function of vehicle mass for ECE (squares) and NAO (circles) pads and gray cast iron discs. Grey triangles and bigger squares with border are three dedicated studies that modified the vehicle mass and the dashed lines show their trendline assuming linear correlation for each study. The dotted lines give the correlation line of the ECE and NAO brakes of Table 2.
Figure 2. PM10 emissions in function of vehicle mass for ECE (squares) and NAO (circles) pads and gray cast iron discs. Grey triangles and bigger squares with border are three dedicated studies that modified the vehicle mass and the dashed lines show their trendline assuming linear correlation for each study. The dotted lines give the correlation line of the ECE and NAO brakes of Table 2.
Atmosphere 15 00097 g002
Atmosphere 15 00097 g003
Figure 3. PM10 emission in function of vehicle mass for ECE or NAO pads and gray cast iron discs, or CC and HMC disks. With asterisks the OICA data (mix of brakes and vehicles). The dotted line is the correlation line of the OICA data.
Figure 3. PM10 emission in function of vehicle mass for ECE or NAO pads and gray cast iron discs, or CC and HMC disks. With asterisks the OICA data (mix of brakes and vehicles). The dotted line is the correlation line of the OICA data.
Atmosphere 15 00097 g003
Table 1. Emission factors of full friction brakes at vehicle level for mass (mg/km/V) or particle number (#/km/V).
Table 1. Emission factors of full friction brakes at vehicle level for mass (mg/km/V) or particle number (#/km/V).
YearRef.TypePadVehicle or MassPM10
mg/km/V		PM2.5
mg/km/V		PN × 109
#/km/V		Comments
1983[29]DAsbestosn/a7.8--Dyno, urban
2000[44]DSM × 5PCs3.1–5.22.1–3.5-Estim. from pad life
2000[44]D + DrumSM × 2PT7.55.5-Estim. from pad life
2002[45]allallall7.0--Estim. from 40% of wear rate
2003[46]DLMMid PC8.2 mg/stop/B--Wind tunnel, urban driving
2003[46]DSMPT2.0 mg/stop/B--
2003[46]DNAOLarge PC1.8 mg/stop/B--
2004[32]Dn/aPC1.8 Mass loss (Motorway)
2004[32]D + Drumn/aPC × 44.7–20.5 Mass loss (Urban − Motorw.)
2008[47]n/aNAO × 320005.8 mg/stop/V-n/aEstimated from pad life
2015[48]DNAOPC0.670.53n/aDyno, JC08 cycle
andandDNAOPC1.381.00n/aDust monitor
2016[49]DrumNAOMid PT0.160.11n/a
2017/18[14,50]DNAO15008.5–9.2 mg/stop/B1530/stop/BDyno, SAE J2707, ELPI
2017/20[36,50]DLM × 4150013.7–46.4 mg/stop/B80–910/stop/BDyno, SAE J2707, ELPI
2019[51]D + HMCLMMid PC4.0–6.0 **-570–3700 **On road, LACT, DustTrak
2019[52]D + HMCproto1600--10Chassis, LACT, CS + CPC10
2019[53]Dn/aVan 2286--5–20On-road, PEMS23
2021[54]Dn/a1840--33Dyno, WLTP-B, ELPI
2020[55]DLMn/a1.9–3.1--Dyno, WLTP-E, OPC
2020[55]DNMn/a0.2–2.3--Dyno, WLTP-E, OPC
2021[56]DLMn/a7–21-7–30Dyno, WLTP-E, ELPI
2021[56]DNMn/a1.5–5.0-23–47Dyno, WLTP-E, ELPI
2021[57]DLMMid PC7.4--Dyno, WLTP-E
2022[58]DLM1300 *17.1 **6.3-Dyno, WLTP-E, APS
2022[58]DNAO1300 *3.3 **2.3-Dyno, WLTP-E, APS
2022[41]DLM1400 *7.0--Dyno, WLTP-B, ELPI
2022[59]DECE23102.5–4.5-5.6–14On road, chassis, ELPI
2023[60]DECE180010.2 **3.1 **37 **On road RDE, PM, CPC
2023[61]DSMn/a9.3–15.32.0–3.5-Dyno, RDE braking, PM
2023[61]DCeramicn/a3.10.7-Dyno, RDE braking, PM
* estimated from rotational inertia. ** multiplied by 2.83 to convert front brake emissions to vehicle emissions. APS = aerodynamic particle sizer; B = brake; CPC10 = condensation particle counter > 10 nm; CS = catalytic stripper; D = disc (GCI); E = exhaust; ELPI = electrical low pressure impactor; GCI = gray cast iron; HMC = hard metal coated; LACT = Los Angeles City Traffic; LM = low metallic; NAO = non-asbestos organic; n/a = not available; NM = non-metallic; OPC = optical particle counter; PC = passenger car; PEMS23 = portable emissions measurement system > 23 nm; PM = particulate matter (gravimetric method); PT = pick-up truck; RDE = real driving emissions; SM = semi-metallic; WLTP = worldwide harmonized light vehicles test procedure cycle.
Table 2. Emission factors of full friction brakes for mass (mg/km/B) or particle number (#/km/B) measured according to the Brakes GTR 24 for light-duty vehicles, i.e., with the WLTP-B (worldwide harmonized light vehicles test procedure brake cycle), unless otherwise specified. Values in brackets were assumed.
Table 2. Emission factors of full friction brakes for mass (mg/km/B) or particle number (#/km/B) measured according to the Brakes GTR 24 for light-duty vehicles, i.e., with the WLTP-B (worldwide harmonized light vehicles test procedure brake cycle), unless otherwise specified. Values in brackets were assumed.
YearRef.AxleTypePadMass
kg		PM10
mg/km/B		PM2.5
mg/km/B		PN × 109
#/km/B		Comments
2019[62]FDLM15004.6-4.9Mid-sized, LACT cycle
2019[63]FDECE15004.51.51.5Mid-sized
2019[64]FDECE12002.5 *1.2 *0.8 *City car
2019[64]FDNAO12001.2 *0.7 *0.5 *City car
2019[64]FDNAO12000.4 *0.2 *0.1 *City car
2020[65]FDECE17507.62.54.5Also [66]
2020[65]FDECE215012.24.88.7
2020[67]FDNAO25001.20.51.1Pick-up truck (8% payload)
2020[67]FDNAO25000.70.40.6Pick-up truck (8% payload)
2020[67]FDNAO29500.80.50.8Pick-up truck (67% payload)
2020[67]FDLM25004.31.52.9Pick-up truck (8% payload)
2020[67]FDLM29507.12.13.2Pick-up truck (67% payload)
2020[67]FDNAO21822.2 *1.0 *-Mini van
2020[67]FDNAO16512.0 *0.9 *-Class C
2020[67]FDNAO16551.80.61.2Class C
2020[67]FDNAO16551.20.41.0Class C
2020[67]FDLM16552.30.72.4Class C
2020[67]FDNAO13473.21.3-Compact
2020[68]FDECEn/a--3.1
2020[68]FDNAOn/a--0.8
2021[23]FDNAO20000.10.05-
2021[69,70]FDECE(1700)8.54.53.5Medium sedan
2021[69,70]FCCECEopt(1700)2.21.11.5Medium sedan
2021[71]FDLM22504.72.41.0Class J
2021[71]FHMCLM22502.11.21.3Class J
2021[71]FCCLM22501.40.90.8Class J
2021[71]FDLM225012.46.04.6Class J
2021[71]FHMCLM22503.41.80.5Class J
2021[71]FCCLM22501.20.80.6Class J
2022[72]FDECE18004.51.453.4Luxury sedan
2022[25]FDLM20004.22.1
2022[25]FDNAO20001.20.5-
2023[10,73]FDECE16006.02.02.2Class C
2023[10,73]FDNAO16002.30.71.0Class C (as above)
2023[10,73]FDECE166810.73.88.6Class J
2023[10,73]FDECE26239.13.13.3SUV
2023[10,73]RDrumn/a12530.50.31.7Super mini
2023[10,73]FDECE25007.73.05.8LCV (28% payload)
2023[10,73]FDECE33909.44.011.1LCV (90% payload)
2023[28]FDLM16605.32.84.3Class C
2023[28]FDNAO16603.92.21.8Class C
2023[28]RDECE16601.50.95.1Class C
2023[28]RDrum(LM)20411.10.82.8Class C
2023[28]RDrum(LM)20410.70.61.1Class C
2023[28]RDrum(NAO)20410.30.30.5Class C
2023[28]FDECE21137.63.53.9Class J
2023[28]FHMCECEopt21131.61.01.4Class J
2023[60]FDECE20274.11.22.1Luxury sedan
2023[74]FDECE18406.51.80.5Japanese market
2023[75]FDLM18202.3--Corrected with ×0.7/2
2023[75]FDNAO18201.1--Corrected with ×0.7/2
2023[75]FDLM22501.3--Corrected with ×0.7/2
2023[75]FDHMC22500.5--Corrected with ×0.7/2
2023[76]FDECE15007.3--Segment D
2023[76]FDECE12505.4--Segment B
2023[76]FDECE12006.9--Segment B
2023[76]FDECE12505.1--Segment B
2023[61]FD(SM)n/a5.71.2-Average of two
2023[61]FDCeramicn/a3.20.8-Estimated from figure
2023[77]FDECE12403.71.3--
2023[77]FDNAO12401.40.6--
2023[78]FDNAO15330.80.20.1-
* Divided by 2.83 to convert vehicle emission to brake corner. B = brake; CC = carbon ceramic; D = disc (GCI); ECE = Economic Commission for Europe; GCI = gray cast iron; HMC = hard metal coated discs; LACT = Los Angeles City Traffic; LCV = light-commercial vehicle; LM = low metallic; NAO = non-asbestos organic; SUV = sports utility vehicle.
Table 3. Airborne and particulate matter PM10 fractions of total mass loss for gray cast iron disc brakes. Some information about the studies can be found in Table 2.
Table 3. Airborne and particulate matter PM10 fractions of total mass loss for gray cast iron disc brakes. Some information about the studies can be found in Table 2.
YearRef.Airborne/Mass LossPM10/Mass LossComment
1973-2–22%-Cited in [29]
1980-55%-Cited in [29]
1983[29]32%--
2000[44]16–35% *14–30%86% from airborne
2003[46]50%40%80% from airborne
2008[47]63%60–62%95–98% from airborne
2016[49]2–29%-
2017[50]35–58%-
2019[63]-57%Based on recovered deposited mass
2020[36]37%-
2020[67]<10%-
2019[62]49%-
2021[71]-24–51%30–40% with CC and HMC
2022[25]-28%Both LM and NAO
2023[10]-35–48%21% for Drum
2023[28]-40%
2023[76]-48–57%
2023[61]-66%Six SM and ceramic pads
2023[77]-35–40%Both ECE and NAO
2023[78]-25%NAO
* correcting for particle losses, it arrives at 64% [46]. CC = carbon ceramic; HMC = hard metal coated discs; LM = low metallic; NAO = non-asbestos organic; SM = semi-metallic.
Table 4. Potential reduction of brake emissions with NAO (non-asbestos organic) pads compared to ECE pads.
Table 4. Potential reduction of brake emissions with NAO (non-asbestos organic) pads compared to ECE pads.
YearRef.PM10PM2.5PNComment
2003[46]78%---
2018[14]65%---
2019[64]52–84%42–83%40–88%2 × NAO
2020[67]84–89%73–76%75–79%Pickup truck
2020[67]22–48%14–43%50–58%2 × NAO
2020[68]--75%-
2021[69]--75%-
2022[58]80%64%--
2022[25]72–77%64–78%-3 cycles
2023[10,73]62%65%55%-
2023[28]26%22%58%-
2023[75]55%---
2023[81]--64%-
2023[77]62%55%--
Table 5. Potential reduction of emissions replacing gray cast iron (GCI) disks with carbon-ceramic (CC) or hard metal coated (HMC) disks.
Table 5. Potential reduction of emissions replacing gray cast iron (GCI) disks with carbon-ceramic (CC) or hard metal coated (HMC) disks.
YearRef.WearPM10PM2.5PNComment
2017[84]43–72%38–57% 44–67%HMC 1
2019[18]32%---HMC 2
2020[85]56%---HMC 3
2020[17]21%--57%HMC 4
2021[16]78–84%94% *-83–91%CC
2021[69]-74%76%57%CC (+opt. pad)
2021[71]-55%50%(30% incr.)HMC 5
2021[71]-70%63%10%CC
2021[71]-73%70%89%HMC 5
2021[71]-90%87%87%CC
2023[28]-79%71%64%CC
2023[75] 63%--HMC
1 WC/CoCr; 2 Cr2O3-40%TiO2; 3 20NiCrBSi-WC12Co; 4 Ni-SF, SFTC; 5 WC; * determined with an electrical low pressure impactor (ELPI). CC = carbon ceramic; HMC = hard metal coated.
Table 6. Brake particles collection efficiency of various filters.
Table 6. Brake particles collection efficiency of various filters.
YearRef.PMPN Comments
2016[86]92%-PassiveAt ventilated disc
2020[87]68–95%50–90%ActiveGrooved pad. 84% at WLTP-B
2020[88]75%40–50%ActiveGrooved pad. Negligible improvement with passive
2021[89]20–39%-PassiveCan increase with smaller gap to the disc
2022[90]53%-PassiveCeramic filter porosity 52%
2022[91]-50–80%PassiveInertial separator. Above 2.2 μm. WLTP-B
2022[91]60–75%>50%PassiveInertial separator and ESP. Above 0.5 μm. WLTP-B
2023[92]61%-ActiveWLTP-B. Collection efficiency 80% with continuous sampling
2023[76]77%-ActiveWLTP-B. Collection efficiency 84% with continuous sampling
ESP = electrostatic precipitator; PM = particulate matter; PN = particle number; WLTP-B = worldwide harmonized light vehicles test procedure brake cycle.
Table 7. Electrified vehicles stock and activity share in 2020′s fleet based on European Commission’s (EC) impact assessment study [4], and expected use of friction brakes depending on the electrification level based on GTR 24. Activity is defined as the multiplication of vehicles and annual km travelled.
Table 7. Electrified vehicles stock and activity share in 2020′s fleet based on European Commission’s (EC) impact assessment study [4], and expected use of friction brakes depending on the electrification level based on GTR 24. Activity is defined as the multiplication of vehicles and annual km travelled.
CategoryPCs
Share		PCs
Activity		LCVs
Share		LCVs
Activity		Regenerative Braking
Petrol53.0%37.5%7.7%3.2%0%
Diesel41.1%57.2%90.5%95.3%0%
HEV1.5%2.0%0.3%0.4%10–48%
PHEV0.4%0.6%0.1%0.1%66%
BEV0.4%0.6%0.3%0.3%83%
other3.6%2.01.2%0.7%0%
BEV = battery electric vehicle; HEV = hybrid electric vehicle; PHEV = plug-in hybrid vehicle.
Table 8. Emission factors of electric vehicles for mass (mg/km/V) or particle number (#/km/V). Percentages in brackets give the emissions reductions compared to their internal combustion engine (ICE) counterpart with full friction braking (i.e., with regenerative braking de-activated).
Table 8. Emission factors of electric vehicles for mass (mg/km/V) or particle number (#/km/V). Percentages in brackets give the emissions reductions compared to their internal combustion engine (ICE) counterpart with full friction braking (i.e., with regenerative braking de-activated).
YearRef.TypePadVehicle or MassPM10
mg/km/V		PM2.5
mg/km/V		PN × 109
#/km/V		Comments
2020[67]DiscNAO16002.0–2.31.0–1.41.3–8.9PHEV
2021[100]Discn/a(1800)0.9--BEV
2023[28]DiscECE16605.7 (−62%)3.4 (−57%)7.3 (−40%)PHEV
2023[28]DiscECE16603.1 (−79%)2.3 (−71%)2.1 (−82%)BEV
2023[101]DiscECE135010.54.5141HEV, Chassis, WLTP-E
2023[102]DiscECE1228--0.5 * (−4%)Chassis, WLTP-B
2023[102]DiscECE1228--0.5 * (−65%)Chassis, WLTP-E
2023[102]DiscECE1228--4 * (<90%)Chassis, RDE
2023[78]DiscNAO15330.3 (−86%)0.14 (−78%)0.05 (−84%)PHEV, WLTP-B **
* back-calculated to emissions without regenerative braking and multiplied with 2.83/0.83 to convert to total vehicle emissions from rear brake; ** multiplied by 2.83 to convert to vehicle emissions. n/a = not available.
Table 9. Summary of estimated emission factors per brake corner for mass (mg/km/B) and particle number (#/km/B).
Table 9. Summary of estimated emission factors per brake corner for mass (mg/km/B) and particle number (#/km/B).
CategoryMass
kg		PM10
mg/km/B		PM2.5
mg/km/B		PN × 109
#/km/B		Comment
ECE (all)19026.02.53.9Average Table 2
ECE (PCs)17525.82.53.5Average Table 2
ECE (LCVs)28387.12.75.6Average Table 2
ECE 15254.71.93.2Based on Figure 2
ECE (N1-III)17605.52.23.7Based on Figure 2
ECE (N1-III)22507.02.94.7Based on Figure 2
NAO18071.70.80.7Average Table 2
CC and HMC21521.81.11.0Average Table 2
Drum18440.70.51.5Average Table 2
B = brake; CC = carbon-ceramic; ECE = Economic Commission for Europe; HMC = hard metal coated; LCV = light commercial vehicle; NAO = non-asbestos organic; PC = passenger car.
Table 10. Brake emission factors EF at vehicle level for mass (mg/km/vehicle) and particle number (#/km/V) for different disc and pad combinations. Emission factors per brake EFB are given in Table 9. PC = passenger cars; LCV = light commercial vehicles.
Table 10. Brake emission factors EF at vehicle level for mass (mg/km/vehicle) and particle number (#/km/V) for different disc and pad combinations. Emission factors per brake EFB are given in Table 9. PC = passenger cars; LCV = light commercial vehicles.
ScenarioMass
kg		PM10
mg/km/V		PM2.5
mg/km/V		PN
#/km/V		Comments
ECE152513.45.59.1EFB,ECE × 2.83
ECE176015.46.310.5EFB,ECE × 2.83
ECE225019.78.113.4EFB,ECE × 2.83
ECE + Drum176012.25.510.52 × EFB,ECE + 2 × EFB,Drum
ECE + Drum225015.36.712.52 × EFB,ECE + 2 × EFB,Drum
NAOall4.72.22.1EFB,NAO × 2.83
NAO1525–22505.4–7.92.5–3.64.1–6.0−60% from ECE
CC/HMC + NAOall6.93.83.52 × EFB,CC + 2 × EFB,NAO
Electrification share in fleet 2020
PC152513.15.48.9Fleet activity Table 7
LCV225019.68.013.4Fleet activity Table 7
Table 11. Light-duty vehicles brake emissions based on field studies and receptor modelling (mg/km/V). PC = passenger cars; HDV = heavy-duty vehicles.
Table 11. Light-duty vehicles brake emissions based on field studies and receptor modelling (mg/km/V). PC = passenger cars; HDV = heavy-duty vehicles.
YearRef.PM10
mg/km/V		PM2.5
mg/km/V		Comments
2003[110]0–800–5Freeway exits, North Carolina, USA
2004[32]6.9-Tunnel London, UK (13% HDV, incl. tire wear)
2010[111]8.0-Urban, Zurich, CH (9% vans)
2010[111]1.6-Interurban freeway, Zurich, CH (15% vans)
2016[112]1.6–6 Urban and ring road, Paris, France
2016[113]3.8–4.4-Tunnel, London, UK (8% HDVs)
2019[114]9.2-Grenoble, France (PC and HDV)
2020[115]0.3–1.00.1–0.5Tunnels in four cities, China
2021[116]12.9-Urban, London, UK (3.2% HDV)
2023[117]4.4–7.4-Birmingham, UK (3% HDV)
2023[118]-0.28Urban tunnel, Tianjin, China (gasoline)
Table 12. Light-duty vehicles brake emissions based on emission inventories (mg/km/V).
Table 12. Light-duty vehicles brake emissions based on emission inventories (mg/km/V).
YearRef.PM10PM2.5Source
2022[9]124.8EEA, COPERT (PC ICE)
20229.53.8EEA, COPERT (PC HEV)
20226.52.6EEA, COPERT (PC PHEV)
20223.31.3EEA, COPERT (PC BEV)
2022124.8EEA, COPERT (LCV N1-I)
2022176.7EEA, COPERT (LCV N1-II/III)
2020[122]8.43.3NAEI UK (PC)
202013.15.7NAEI UK (LCV)
2020[95]6.22.4Australia, COPERT Australia (ICE)
20204.31.6Australia, COPERT Australia (BEV)
2020[120]13.81.7US EPA, MOVES3 (PC)
202015.31.9US EPA, MOVES3 (LCV)
2021[121]3–101–3CARB, EMFAC (PC)
2021144.5CARB, EMFAC (LCV)
2021[123]9.13.6DCE, CORPEM (PC)
2021[124]10-PBL NL (PC)
BEV = battery electric vehicle; HEV = hybrid electric vehicle; ICE = internal combustion engine; LCV = light commercial vehicle; PC = passenger car; PHEV = plug-in hybrid electric vehicle.
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Giechaskiel, B.; Grigoratos, T.; Dilara, P.; Karageorgiou, T.; Ntziachristos, L.; Samaras, Z. Light-Duty Vehicle Brake Emission Factors. Atmosphere 2024, 15, 97. https://doi.org/10.3390/atmos15010097

AMA Style

Giechaskiel B, Grigoratos T, Dilara P, Karageorgiou T, Ntziachristos L, Samaras Z. Light-Duty Vehicle Brake Emission Factors. Atmosphere. 2024; 15(1):97. https://doi.org/10.3390/atmos15010097

Chicago/Turabian Style

Giechaskiel, Barouch, Theodoros Grigoratos, Panagiota Dilara, Traianos Karageorgiou, Leonidas Ntziachristos, and Zissis Samaras. 2024. "Light-Duty Vehicle Brake Emission Factors" Atmosphere 15, no. 1: 97. https://doi.org/10.3390/atmos15010097

APA Style

Giechaskiel, B., Grigoratos, T., Dilara, P., Karageorgiou, T., Ntziachristos, L., & Samaras, Z. (2024). Light-Duty Vehicle Brake Emission Factors. Atmosphere, 15(1), 97. https://doi.org/10.3390/atmos15010097

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop