Characteristics of PM_2.5 mass concentrations and chemical species in urban and background areas of China: emerging results from the CARE-China network

The “Campaign on Atmospheric Aerosol Research” network of China (CARE-China) is a long-term project for the study of the spatio-temporal distributions of physical aerosol characteristics as well as the chemical components and optical properties of aerosols over China. This study presents the first long-term data sets from this project, including 3 years of observations of online PM_2.5 mass concentrations (2012–2014) and 1 year of observations of PM_2.5 compositions (2012–2013) from the CARE-China network. The average PM_2.5 concentration at 20 urban sites is 73.2 µg m⁻³ (16.8–126.9 µg m⁻³), which was 3 times higher than the average value from the 12 background sites (11.2–46.5 µg m⁻³). The PM_2.5 concentrations are generally higher in east-central China than in the other parts of the country due to their relatively large particulate matter (PM) emissions and the unfavourable meteorological conditions for pollution dispersion. A distinct seasonal variability in PM_2.5 is observed, with highs in the winter and lows during the summer at urban sites. Inconsistent seasonal trends were observed at the background sites. Bimodal and unimodal diurnal variation patterns were identified at both urban and background sites. The chemical compositions of PM_2.5 were analysed at six paired urban and background sites located within the most polluted urban agglomerations – North China Plain (NCP), Yangtze River delta (YRD), Pearl River delta (PRD), North-east China region (NECR), South-west China region (SWCR) – and the cleanest region of China – the Tibetan Autonomous Region (TAR). The major PM_2.5 constituents across all the urban sites are organic matter (OM, 26.0 %), ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (17.7 %), mineral dust (11.8 %), ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (9.8 %), ${\mathrm{NH}}_{\mathrm{4}}^{+}$ (6.6 %), elemental carbon (EC) (6.0 %), Cl⁻ (1.2 %) at 45 % RH and unaccounted matter (20.7 %). Similar chemical compositions of PM_2.5 were observed at background sites but were associated with higher fractions of OM (33.2 %) and lower fractions of ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (8.6 %) and EC (4.1 %). Significant variations of the chemical species were observed among the sites. At the urban sites, the OM ranged from 12.6 µg m⁻³ (Lhasa) to 23.3 µg m⁻³ (Shenyang), the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ ranged from 0.8 µg m⁻³ (Lhasa) to 19.7 µg m⁻³ (Chongqing), the ${\mathrm{NO}}_{\mathrm{3}}^{-}$ ranged from 0.5 µg m⁻³ (Lhasa) to 11.9 µg m⁻³ (Shanghai) and the EC ranged from 1.4 µg m⁻³ (Lhasa) to 7.1 µg m⁻³ (Guangzhou). The PM_2.5 chemical species at the background sites exhibited larger spatial heterogeneities than those at urban sites, suggesting different contributions from regional anthropogenic or natural emissions and from long-range transport to background areas. Notable seasonal variations of PM_2.5-polluted days were observed, especially for the megacities in east-central China, resulting in frequent heavy pollution episodes occurring during the winter. The evolution of the PM_2.5 chemical compositions on polluted days was consistent for the urban and nearby background sites, where the sum of sulfate, nitrate and ammonia typically constituted much higher fractions (31–57 %) of PM_2.5 mass, suggesting fine-particle pollution in the most polluted areas of China assumes a regional tendency, and the importance of addressing the emission reduction of secondary aerosol precursors including SO₂ and NO_x. Furthermore, distinct differences in the evolution of $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ ratio and OC∕EC ratio on polluted days imply that mobile sources and stationary (coal combustion) sources are likely more important in Guangzhou and Shenyang, respectively, whereas in Beijing it is mobile emission and residential sources. As for Chongqing, the higher oxidation capacity than the other three cities suggested it should pay more attention to the emission reduction of secondary aerosol precursors. This analysis reveals the spatial and seasonal variabilities of the urban and background aerosol concentrations on a national scale and provides insights into their sources, processes and lifetimes.

1 Introduction

Atmospheric fine-particulate matter (PM_2.5) is a complex heterogeneous mixture. Its physical size distribution and chemical composition change in time and space and are dependent on the emission sources, atmospheric chemistry and meteorological conditions (Seinfeld and Pandis, 2016). Atmospheric PM_2.5 has known important environmental impacts related to visibility degradation and climate change. Because of their abilities to scatter and absorb solar radiation, aerosols degrade visibility in both remote and urban locations and can have direct and indirect effects on the climate (IPCC, 2013). Fine atmospheric particles are also a health concern and have been linked to respiratory and cardiovascular diseases (Sun et al., 2010; Viana et al., 2008; L. W. Zhang et al., 2014). The magnitudes of the effects of PM_2.5 on all these systems depend on their sizes and chemical compositions. Highly reflective aerosols, such as sulfates and nitrates, result in direct cooling effects, while aerosols with low single-scattering albedos absorb solar radiation and include light-absorbing carbon, humic-like substances and some components of mineral soils (Hoffer et al., 2006). The health impacts of these particles may also differ with different aerosol compositions (Zimmermann, 2015); the adverse health effects specifically associated with organic aerosols have been reported by Mauderly and Chow (2008). Therefore, the uncertainties surrounding the roles of aerosols in climate, visibility and health studies can be significant because chemical composition data may not be available for large spatial and temporal ranges.

Reducing the uncertainties associated with aerosol effects requires observations of aerosol mass concentrations and chemical speciation from long-term spatially extensive ground-based networks. Continental sampling using ground-based networks has been conducted in North America (Hand et al., 2012) and Europe (Putaud et al., 2010) since the 1980s, such as via the U.S. EPA's Chemical Speciation Network (CSN), the Interagency Monitoring of Protected Visual Environments (IMPROVE) network, the Clean Air Status and Trends Network (CASTNET) and the National Atmospheric Deposition Program (NADP). Previous studies suggest that spatial and temporal patterns of PM_2.5 mass concentrations and chemical species can vary significantly depending on species and location. For example, Malm et al. (2004) reported the 2001 monthly mean speciated aerosol concentrations from the IMPROVE monitors across the United States and demonstrated that ammonium sulfate concentrations were highest in the eastern United States and dominated the fine-particle masses in the summer. Clearly decreasing gradients of the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ contributions to PM₁₀ were observed in Europe when moving from rural to urban to kerbside sites (Putaud et al., 2010). Although large disparities of PM_2.5 pollution levels exist between megacities in developing and developed countries, the PM_2.5 annual mass concentrations in the former are approximately 10 times greater than those of the latter (Cheng et al., 2016); however, ground-based networks that consistently measure PM_2.5 mass concentrations and chemical compositions remain rare in densely populated regions of developing countries.

China is the world's most populous country and has one of the fastest-growing economies. Fast urbanization and industrialization can cause considerable increases in energy consumption. China's energy consumption increased 120 % from 2000 to 2010. Coal accounted for most of the primary energy consumption (up to 70 %) (Department of Energy Statistics, National Bureau of Statistics of China, 2001, 2011). Meanwhile, the emissions of high concentrations of numerous air pollutants cause severe air pollution and haze episodes. For example, a heavy air pollution episode occurred in north-eastern China in January 2013, wherein the maximum hourly averaged PM_2.5 exceeded 600 µg m⁻³ in Beijing (Wang et al., 2014). This event led to considerable public concern. However, ground-based networks that consistently measure PM_2.5 mass concentrations and chemical compositions in China are limited. Although there were some investigations of the various aerosol chemical compositions in China (He et al., 2001; Huang et al., 2013; Li et al., 2012; Liu et al., 2015; Pan et al., 2013; Tao et al., 2014; Wang et al., 2013; Yang et al., 2011; P. S. Zhao et al., 2013; Zhou et al., 2012), earlier studies were limited in their temporal and spatial scopes, with very few having data exceeding 1 year while covering various urban and remote regions of the country (Zhang et al., 2012; Y. Q. Wang et al., 2015). Indeed, before 2013, the Chinese national monitoring network did not report measurements of PM_2.5 or its chemical composition, and thus ground-based networks for atmospheric fine-particulate matter measurements at regional and continental scales are needed, as these networks are essential for the development and implementation of effective air pollution control strategies and are also useful for the evaluation of regional and global models and satellite retrievals.

To meet these sampling needs, the Campaign on Atmospheric Aerosol Research network of China (CARE-China) was established in late 2011 for the study of the spatio-temporal distributions of the physical and chemical characteristics and optical properties of aerosols (Xin et al., 2015). This study presents the first long-term data set to include 3 years of observations of online PM_2.5 mass concentrations (2012–2014) and 1 year of observations of PM_2.5 compositions (2012–2013) from the CARE-China network. The purpose of this work is to (1) assess the PM_2.5 mass concentration levels, including the seasonal and diurnal variation characteristics at the urban, rural and regional background sites; (2) obtain the seasonal variations of the PM_2.5 chemical compositions at paired urban–background sites in the most polluted regions and clean areas; and (3) identify the occurrences and chemical signatures of haze events via an analysis of the temporal evolutions and chemical compositions of PM_2.5 on polluted days. These observations and analyses provide general pictures of atmospheric fine-particulate matter in China and can also be used to validate model results and implement effective air pollution control strategies.

2 Materials and methods

2.1 An introduction to the PM_2.5 monitoring sites

The PM_2.5 data from 36 ground observation sites used in this study were obtained from the CARE-China network (Campaign on Atmospheric Aerosol Research network of China), which was supported by the Chinese Academy of Sciences (CAS) Strategic Priority Research Program grants (Category A). Xin et al. (2015) provided an overview of the CARE-China network, the cost-effective sampling methods employed and the post-sampling instrumental methods of analysis. Four more ground observation sites (Shijiazhuang, Tianjin, Ji'nan and Lin'an) from the Forming Mechanism and Control Strategies of Haze in China group (Wang et al., 2014) were also included in this study to better depict the spatial distributions and temporal variations of PM_2.5 in eastern China. A comprehensive 3-year observational network campaign was carried from 2012 to 2014 out at these 40 ground observation sites. Figure 1 and Table 1 respectively show the geographic distribution and details of the network stations, which include 20 urban sites, 12 background sites and 8 rural/suburban sites. The urban sites, such as those at Beijing, Shanghai and Guangzhou, are surrounded by typical residential areas and commercial districts. The background sites are located in natural reserve areas or scenic spots, which are far away from anthropogenic emissions and are less influenced by human activities. Rural/suburban sites are situated in rural and suburban areas, which may be affected by agricultural activities, vehicle emissions and some light industrial activities. These sites are located in different parts of China and can provide an integrated insight into the characteristic of PM_2.5 over China.

Table 1 Geographic information and 3-year mean PM_2.5 concentration of the monitoring stations.

Figure 1 Locations and the averaged PM_2.5 concentrations of the 40 monitoring stations during (a) 2012–2014, (b) spring, (c) summer, (d) autumn and (e) winter. The site codes related to the observation stations can be found in Table 1.

2.2 Online instruments and data sets

A tapered element oscillating microbalance (TEOM) was used for the PM_2.5 measurements at 34 sites within the network (Table S1 in the Supplement). This system was designated by the US Environmental Protection Agency (USEPA) as having a monitoring compliance equivalent to the National Ambient Air Quality standard for particulate matter (Patashnick and Rupprecht, 1991). The measurement ranges of the TEOMs were 0–5 g m⁻³, with a 0.1 µg m⁻³ resolution and precisions of ±1.5 (1 h average) and  ± 0.5 µg m⁻³. The models used in the network are TEOM 1400a and TEOM 1405, and the entire system was heated to 50 ^∘C; thus, a loss of semi-volatile compounds cannot be avoided. Our previous study showed that mass concentrations up to 25 % lower were found for select daily means than those observed with gravimetric filter measurements, depending on the ammonium-nitrate levels and ambient temperatures (Liu et al., 2015). The errors of the TEOM measurements are systematic in that they are always negative. Thus, these errors may not be important for the study of the spatial distributions and temporal variations of PM_2.5. The other six sites of the network (Shanghai, Guangzhou, Chengdu, Xi'an, Urumchi and Qinghai Lake) were equipped with beta gauge instruments (EBAM, Met One Instruments Inc., Oregon). The measurement range of EBAM is 0–1000 µg m⁻³, with a precision of 0.1 µg m⁻³ and a resolution of 0.1 µg m⁻³. The filters were changed every week, and the inlet was cleaned every month. The flow rates were also monitored and concurrently calibrated. A year-long intercomparison of daily PM_2.5 mass concentrations measured by TEOM and EBAM was conducted at the Beijing site (Fig. S1a), and the results showed that these two online instruments correlated well (R²=0.90, P<0.01). TEOM reported approximately 24 % lower mass concentration than EBAM, and the difference could be explained by the loss of semi-volatile materials from TEOM (Zhu et al., 2007).

2.3 Filter sampling and chemical analysis

In this study, filter sampling was conducted at the five urban sites of Beijing, Guangzhou, Lhasa, Shenyang and Chongqing as well as at the six background sites of Xinglong, Lin'an, Dinghu Mountain, Namsto, Changbai Mountain and Gongga Mountain. The Automatic Cartridge Collection Unit (ACCU) system of Rupprecht & Patashnick Co. with 47 mm diameter quartz fibre filters (Pall Life Sciences, Ann Arbor, MI, USA) was deployed in Beijing to collect the PM_2.5 samplers (Z. R. Liu et al., 2016). Similar to the ACCU system, a standard 47 mm filter holder with quartz fibre filters (Pall Life Sciences, Ann Arbor, MI, USA) was placed in the bypass line of TEOM 1400a and TEOM 1405 using quick-connect fittings and was used to collect the PM_2.5 samplers of the other nine sites, except Guangzhou and Lin'an. Each set of the PM_2.5 samples was continuously collected over 48 h on the same days of each week, generally starting at 08:00. The flow rates were typically 15.6 L min⁻¹. For the Guangzhou site, the fine particles were collected on Whatman quartz fibre filters using an Andersen model SA235 sampler (Andersen Instruments Inc.) with an airflow rate of 1.13 m³ min⁻¹. The sampling lasted 48 h for the first three samples and 24 h for the rest samples, generally starting at 08:00. For the Lin'an site, a medium volume PM_2.5 sampler (model: TH-150CIII, Tianhong Instrument CO., Ltd. Wuhan, China) was used to collect 24 h of PM_2.5 aerosols on 90 mm quartz fibre filters (QMA, Whatman, UK) once every 6 days (Xu et al., 2017). The sampling periods of these 11 urban and background sites are shown in Table S1.

All the filters were heat treated at 500 ^∘C for at least 4 h for cleaning prior to filter sampling. The PM_2.5 mass concentrations were obtained via the gravimetric method with an electronic balance with a detection limit of 0.01 mg (Sartorius, Germany) after stabilizing at a constant temperature (20 ± 1 ^∘C) and humidity (45 % ± 5 %). PM_2.5 mass concentrations measured by gravimetric method correlated well with the online instruments (TEOM and EBAM) as showed in Fig. S1b. On average, PM_2.5 mass concentration measured by the filter sampling was approximately 9 % higher than the online instruments. Three types of chemical species were measured using the methods described in Xin et al. (2015). Briefly, the organic carbon (OC) and elemental carbon (EC) values were determined using a thermal/optical reflectance protocol using a DRI model 2001 carbon analyser (Atmoslytic, Inc., Calabasas, CA, USA) with the thermal/optical reflectance (TOR) method. A circle piece of 0.495 cm² was cut off from the filters and was sent into the thermal optical carbon analyser. In a pure helium atmosphere, OC1, OC2, OC3 and OC4 are produced stepwise at 140, 280, 480 and 580^∘, followed by EC1 (540^∘), EC2 (780^∘) and EC3 (840^∘) in a 2 % oxygen-contained helium atmosphere. Eight main ions, including K⁺, Ca²⁺, Na⁺, Mg²⁺, ${\mathrm{NH}}_{\mathrm{4}}^{+}$, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and Cl⁻, were measured via ion chromatography (using a Dionex DX 120 connected to a DX AS50 autosampler for anions and a DX ICS90 connected to a DX AS40 autosampler for cations). One-quarter of each filter substrate was extracted with 25 mL deionized water in a PET vial for 30 min. Before performing a targeted sample analysis, a standard solution and blank test were performed, and the correlation coefficient of the standard samples was more than 0.999. The detection limits for all anions and cations, which were calculated as 3 times the standard deviations of seven replicate blank samples, are all lower than 0.3 µg m⁻³ (Liu et al., 2017). The microwave acid digestion method was used to digest the filter samples into liquid solution for elemental analysis. One quarter of each filter sample was placed in the digestion vessel with a mixture of 6 mL HNO₃, 2 mL H₂O₂ and 0.6 mL HF and was then exposed to a three-stage microwave digestion procedure from a Microwave-Accelerated Reaction System (MARS, CEM Corporation, USA). After that, 18 elements, including Mg, Al, K, Ca, V, Cr, Mn, Fe, Co, Ni, Cu, Zn, As, Se, Ag, Cd, Tl and Pb, were determined by Agilent 7500a inductively coupled plasma mass spectrometry (ICP-MS, Agilent Technologies, Tokyo, Japan). Quantification was carried out by the external calibration technique using a set of external calibration standards (Agilent Corporation) at concentration levels close to that of the samples. The relative standard deviation for each measurement (repeated twice) was within 3 %. The method detection limits (MDLs) were determined by adding 3 standard deviations of the blank readings to the average blank values (Yang et al., 2009). Quality control and quality assurance procedures were routinely applied for all carbonaceous, ion and elemental analyses.

3 Results and discussions

3.1 Characteristics of PM_2.5 mass concentrations at urban and background sites

3.1.1 Average PM_2.5 levels

The location, station information and average PM_2.5 concentrations from the 40 monitoring stations are shown in Fig. 1 and Table 1. The highest PM_2.5 concentrations were observed at the urban stations of Xi'an (125.8 µg m⁻³), Taiyuan (111.5 µg m⁻³), Ji'nan (107.5 µg m⁻³) and Shijiazhuang (105.1 µg m⁻³), which are located in the most polluted areas of the Guanzhong Plain (GZP) and the North China Plain (NCP). Several studies have revealed that the enhanced PM_2.5 pollution of the GZP and NCP are not only due to the primary emissions from local sources such as the local industrial, domestic and agricultural sources but are also due to secondary productions (Huang et al., 2014; Guo et al., 2014; Wang et al., 2014). Furthermore, the climates of the GZP and NCP are characterized by stagnant weather with weak winds and relatively low boundary layer heights, leading to favourable atmospheric conditions for the accumulation, formation and processing of aerosols (Chan and Yao, 2008). Note that the averaged PM_2.5 concentration in Beijing and Tianjin was approximately 70 µg m⁻³, which is much lower than at the other cities, including Ji'nan and Shijiazhuang in the NCP, possibly because Beijing and Tianjin are located in the northern part of the NCP, far from the intense industrial emission area that is mainly located in the southern part of the NCP. Interestingly, the average PM_2.5 concentrations at Yucheng (102.8 µg m⁻³) and Xianghe (83.7 µg m⁻³) were even higher than most of those from the urban stations. Although Yucheng is a rural site, it is located in an area with rapid urbanization near Ji'nan and is therefore subjected to the associated large quantities of air pollutants. In addition, Xianghe is located between Beijing and Tianjin and is influenced by regionally transported contributions from nearby megacities and the primary emissions from local sources. Yantai is a coastal city with relatively low PM concentrations compared to those from inland cities on the NCP.

The PM_2.5 concentrations were also high in the Yangtze River delta (YRD), which is another developed and highly populated city cluster area like the NCP (Fu et al., 2013). The average PM_2.5 values of the three urban stations of Shanghai, Wuxi and Hefei were 56.2, 65.2 and 80.4 µg m⁻³, which are comparable to those of the megacities of Beijing and Tianjin in the NCP. Due to the presence of fewer coal-based industries and dispersive weather conditions, the PM_2.5 concentrations of the Pearl River delta (PRD) are generally lower than those of the other two largest city clusters in China, such as those from the NCP and YRD. The average PM_2.5 value at Guangzhou was 44.1 µg m⁻³, which was similar to the PM_2.5 values of the background stations from the NCP and YRD. Shenyang, the capital of the province of Liaoning, is located in the North-east China region (NECR), which is an established industrial area. High concentrations of trace gases and aerosol scattering in the free troposphere have been observed via aircraft observations and are due to regional transport and heavy local industrial emissions (Dickerson et al., 2007). In the present study, the average PM_2.5 concentration of Shenyang was 77.6 µg m⁻³. Meanwhile, Hailun, which is a rural site in the NECR, had an average PM_2.5 concentration of 41.6 µg m⁻³, which was much lower than that of the rural site of Yucheng in the NCP.

High aerosol optical depths and low visibilities have been observed in the Sichuan Basin (Zhang et al., 2012), which is located in the South-west China region (SWCR). The poor dispersion conditions and heavy local industrial emissions make this another highly polluted area in China. In the present study, the average PM_2.5 concentration in Chengdu was measured as 102.2 µg m⁻³, which is much higher than the averages from the megacities of Beijing, Shanghai and Guangzhou but is comparable to those of Ji'nan and Shijiazhuang. Chongqing, another megacity located in the SWCR, however, showed much lower PM_2.5 values than Chengdu. Urumqi, the capital of the Uighur Autonomous Region of Xinjiang, located in north-western China, experiences air pollution due to its increasing consumption of fossil fuel energy and steadily growing fleet of motor vehicles (Mamtimin and Meixner, 2011). The average PM_2.5 concentration measured in Urumqi is 104.1 µg m⁻³, which is comparable to those of the urban sites in the GZP and NCP. The similarity among the PM_2.5 values for Cele, Dunhuang and Fukang is due to their location, being far from regions with intensive economic development but strongly affected by sandstorms and dust storms due to their proximity to dust source areas. For example, the average PM_2.5 concentration in Cele during the spring (200.7 µg m⁻³) was much greater than those of the other three seasons. Lhasa, the capital of the Tibet Autonomous Region (TAR), is located in the centre of the Tibetan Plateau at a very high altitude of 3700 m. The PM_2.5 concentrations in Lhasa were low, with average values of 30.6 µg m⁻³ because of its relatively small population and few industrial emissions.

Much lower PM_2.5 concentrations were observed at the background stations, the values of which ranged from 11.2 to 46.5 µg m⁻³. The lowest concentration of PM_2.5 was observed at Namsto, a background station on the TAR with nearly no anthropogenic effects. The highest PM_2.5 concentration of the background stations was observed at Lin'an, a background station in the PRD. The average PM_2.5 concentration at the urban and background sites in this study are shown as box plots in Fig. S2a. The average PM_2.5 concentration of the background stations (a total of 12 sites) is 28.5 µg m⁻³, and the average concentration of the PM_2.5 values from urban stations (a total of 20 sites) is 73.2µg m⁻³. The latter value is approximately 3 times the former, suggesting the large differences in fine-particle pollution at urban and background sites across China. To further characterize these kinds of differences for different parts of China, six pairs of PM_2.5 values measured from urban and background stations were selected to represent the NCP, YRD, PRD, TAR, NECR and SWCR (Fig. S2). The first three areas (NCP, YRD and PRD) and the last two areas (NECR and SWCR) are the most industrialized and populated regions in China, while TAR is the cleanest area in China. The PM_2.5 concentrations of the background stations in the NCP, YRD and PRD are 39.8 µg m⁻³ (Xinglong), 46.5 µg m⁻³ (Lin'an) and 40.1 µg m⁻³ (Dinghu Mountain) and are much higher than those of the background stations in other parts of China, which are usually below 25 µg m⁻³. All values, especially those observed at urban and rural sites in this study, were much greater than the results from Europe and North America. For urban/suburban sites, average PM_2.5 concentrations of 20.1 µg m⁻³ were reported by Gehrig and Buchmann (2003) from 1998 to 2001 in Switzerland, and average concentrations of 16.3 µg m⁻³ were reported for the period 2008–2009 in the Netherlands (Janssen et al., 2013). Between October 2008 and April 2011, the 20 study areas covered major cities of the European ESCAPE project and showed annual average concentrations of PM_2.5 ranging from 8.5 to 29.3 µg m⁻³, with low concentrations in northern Europe and high concentrations in southern and eastern Europe (Eeftens et al., 2012). Based on a constructed database of PM_2.5 component concentrations from 187 counties in the United States for 2000–2005, Bell et al. (2007) reported an average PM_2.5 value of 14.0 µg m⁻³, with higher values in the eastern United States and California and lower values in the central regions and north-west. For background sites, Putaud et al. (2010) showed that annual average of PM_2.5 ranged from 3 to 22 µg m⁻³ observed from 12 background sites across Europe. In addition, the average PM_2.5 value of 12.6 µg m⁻³ was observed at a regional background site in the western Mediterranean from 2002 to 2010 (Cusack et al., 2012).

Figure 2 Monthly average PM_2.5 concentration (histogram, left coordinate) and the occurrence of substandard days in each month (dotted line, right coordinate) at urban and background sites in the (a) North China plain, (b) Yangtze River delta, (c) Pearl River delta, (d) Tibetan Autonomous Region, (e) North-east China region and (f) South-west China region. The error bar stands for the standard deviation.

3.1.2 Seasonal variations of PM_2.5 mass concentrations

Generally, the PM_2.5 concentrations in urban areas show distinct seasonal variabilities, with maxima during the winter and minima during the summer for most of China (Fig. 1), which is a similar pattern to that of the results reported by Zhang and Cao (2015). In northern China and north-eastern China, the wintertime peak values of PM_2.5 were mainly attributed to the combustion of fossil fuels and biomass burning for domestic heating over extensive areas, which emit large quantities of primary particulates as well as the precursors of secondary particles (He et al., 2001). In addition, new particle formation and the secondary production of both inorganic aerosols and OM could further enhance fine PM abundance (Huang et al., 2014; Guo et al., 2014). Furthermore, the planetary boundary layer is relatively low in the winter, and more frequent occurrences of stagnant weather and intensive temperature inversions cause very bad diffusion conditions, which can result in the accumulation of atmospheric particulates and lead to high-concentration PM episodes (Quan et al., 2014; X. J. Zhao et al., 2013). In southern and eastern China, although the effect of domestic heating is not as important as it is in North China, the weakened diffusion and transport of pollutants from the north due to the activity of the East Asian Winter Monsoon reinforce the pollution from large local emissions in the winter more than in any other season (Li et al., 2011; Mao et al., 2017). For north-western and west-central China, the most polluted season is spring instead of winter due to the increased contribution from dust particles in this desert-like region (Zou and Zhai, 2004), suggesting that the current PM_2.5 control strategies (i.e. reducing fossil/non-fossil combustion-derived VOCs and PM emissions) will only partly reduce the PM_2.5 pollution in western China. PM_2.5 is greatly decreased during the summer in urban areas, which is associated with reduced anthropogenic emissions from fossil fuel combustion and biomass burning domestic heating. Further, the more intense solar radiation causes a higher atmospheric mixing layer, which leads to strong vertical and horizontal aerosol dilution effects (Xia et al., 2006). In addition, increased precipitation in most of China due to the summer monsoon can increase the wet scavenging of atmospheric particles. As a result, PM_2.5 minima are observed in the summer at urban sites.

Figure 3 Diurnal cycles of PM_2.5 at six paired urban and background sites in the (a) North China Plain, (b) Yangtze River delta, (c) Pearl River delta, (d) Tibetan Autonomous Region, (e) North-east China region and (f) South-west China region. Shaded areas represent the error bars and one half of the standard deviation.

The seasonal variations of PM_2.5 at the background sites varied in different parts of China (Fig. 3). Dinghu Mountain and Lin'an showed maximum values in the winter, while Zangdongnan, Qinghai Lake, Xishuangbanna and Mount Everest showed maximum values in the spring. In addition, a summer maximum of PM_2.5 was observed for Xinglong, and an autumn maximum was observed for Tongyu. Changbai Mountain, Gongga Mountain and Namsto showed weak seasonal variabilities. These results suggest different contributions from regional anthropogenic and natural emissions and long-range transport to background stations. The monthly average PM_2.5 concentrations of the urban and background sites in the NCP, YRD, PRD, TAR, NECR and SWCR are further analysed and shown in Fig. 2. The monthly variations of the PM_2.5 concentrations at the background sites in the YRD and PRD were consistent with those of the nearby urban sites, both of which showed maximum values in December (YRD) and January (PRD). The reasons for this similarity are primarily the seasonal fluctuations of emissions, which are already well known due to similar variations of other parameters, including sulfur dioxide and nitrogen oxide, as shown in Fig. S3. In contrast, monthly variations of PM_2.5 at Xinglong showed different trends to those of the nearby urban stations. The maximum value of PM_2.5 at this site was observed in July, while the maximum value in Beijing was observed in January. The reasons for this are not primarily the seasonal fluctuations of emissions, but rather meteorological effects (frequent inversions during the winter and strong vertical mixing during the summer). The Xinglong site is situated at an altitude of 900 m a.s.l., and therefore, during the wintertime, the majority of cases above the inversion layer are protected from the emissions of the urban agglomerations of the NCP. Furthermore, in the NCP area, northerly winds prevail in the winter, while southerly winds prevail in the summer. Thus, in the summer, more air masses from the southern urban agglomerations will lead to high PM_2.5 concentrations in Xinglong. Weak monthly variabilities were observed for Namsto, Changbai Mountain and Gongga Mountain, although remarkable monthly variabilities were found at the nearby cities of Lhasa, Shenyang and Chongqing. The reasons for this difference are mainly that these three sites are elevated, remote and show predominantly meteorological influences.

3.1.3 Diurnal variations of PM_2.5 mass concentrations

To derive important information to identify the potential emission sources and the times at which the pollution levels exceed the proposed standards, hourly data were used to examine the diurnal variabilities of PM_2.5 as well as those of the other major air pollutants. Figure 3 illustrates the diurnal variations of the hourly PM_2.5 concentrations in Beijing, Shanghai, Guangzhou, Lhasa, Shenyang and Chongqing, in the largest megacities in the NCP, YRD, PRD, TAR, NECR and SWCR and in different climatic zones of China. Of the urban sites, Lhasa has the lowest PM_2.5 concentrations but the most significant pronounced diurnal variations of PM_2.5, with obvious morning and evening peaks appearing at 10:00 and 22:00 (Beijing Time) due to the contributions of enhanced anthropogenic activity during the rush hours. The minimum value occurred at 16:00, which is mainly due to a higher atmospheric mixing layer, which is beneficial for air pollution diffusion. This bimodal pattern was also observed in Shenyang and Chongqing, which show morning peaks at 07:00 and 09:00 and evening peaks at 19:00 and 20:00. However, the PM_2.5 values in Beijing, Shanghai and Guangzhou showed much weaker urban diurnal variation patterns, and slightly higher PM_2.5 concentrations during the night than during the day were observed, which can be explained by enhanced emissions from heating and the relatively low boundary layer. Moreover, fine particles emitted from diesel truck traffic, which is allowed only during night-time, would additionally increase the PM_2.5 burden because emission factors of heavy-duty vehicles are 6 times more than those from light-duty vehicles (Westerdahl et al., 2009). Note that the morning peaks in Beijing, Shanghai and Guangzhou were not as large as those of other cities, although both the SO₂ and NO₂ values increased due to increased anthropogenic emissions (Fig. S4). Alternatively, this decreasing trend may be the result of an increasing boundary layer depth. The invisible morning peak of PM_2.5 in these three cities was possibly attributed to the stricter emission standards applied in recent years. As showed in Fig. S5, the morning peak of PM_2.5 in Beijing gradually disappeared or was invisible after a National 5 vehicle emission standard was applied at the beginning of 2013. The same thing would also be observed in Shanghai and Guangzhou, which implemented the same vehicle emission standards followed Beijing, but not for the other cities as the latest vehicle emission standard was usually applied 2–3 years later than for the three megacities. At the urban sites of Beijing, Shanghai and Guangzhou, the PM_2.5 levels started to increase in the late afternoon, which could be explained by the increasing motor vehicle emissions as NO₂ also dramatically increases during the same period.

In the background area of the TAR, significant pronounced diurnal variations of PM_2.5 were observed at Namsto, with a morning peak at 09:00 and an evening peak at 21:00 (Fig. 3d), which are similar to those of the urban site of Lhasa. As there are hardly any anthropogenic activities near Namsto, this kind of diurnal pattern of PM_2.5 may be influenced by the evolution of the planetary boundary layer. Both Gongga Mountain and Lin'an showed the same bimodal pattern of PM_2.5 to that at Namsto. The former site could also be influenced by the planetary boundary layer, while the latter site was not only influenced by the evolution of the planetary boundary layer but would also be highly affected by regional transportation from the YRD. For the background site of the NCP, however, Xinglong showed smooth PM_2.5 variations. As mentioned before, the Xinglong station is located on the mountain and has an altitude of 960 m a.s.l. The mixed boundary layer of the urban area increases in height in the morning and reaches a height of approximately 1000 m in the early afternoon. Then, the air pollutants from the urban area start to affect the station as the vertical diffusion of the airflow and the PM_2.5 concentration reach their maxima at 18:00. Next, the concentration starts to decrease when the mixed boundary layer collapses in the late afternoon, eventually forming the nocturnal boundary layer (Boyouk et al., 2010). Thus, PM_2.5 concentration decreased slowly during the night and morning, reaching a minimum at 10:00. At Dinghu Mountain and Changbai Mountain, the daytime PM_2.5 is greater than that at night-time, with a maximum value occurring at approximately 11:00–12:00. This kind of diurnal pattern of PM_2.5 is mainly determined by the effects of the mountain–valley breeze. Both the Dinghu Mountain and Changbai Mountain stations are located near the mountain. Thus, during daytime, the valley breeze from urban areas carries air pollutants that will accumulate in front of the mountain and cause an increase in the PM concentration. Meanwhile, at night, the fresh air carried by the mountain breeze will lead to the dilution of PM, so low concentrations are sustained during the night. Further support for this pattern comes from the much higher maximum values of PM_2.5 in the winter than those in the summer, as enhanced air pollutant emissions in urban areas are expected in the winter due to heating.

Table 2 Summary of the concentrations of PM_2.5 and its components (µg m⁻³) at urban and background sites.

^a MD: mineral dust. ^b Unaccounted: the difference between the PM_2.5 gravimetric mass and the sum of the PM constituents (OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$, ${\mathrm{NH}}_{\mathrm{4}}^{+}$, Mineral dust and Cl⁻); the numbers in parentheses refer to standard deviations.

Figure 4 Average chemical composition and its seasonal variations of PM_2.5 at (a, c) urban sites and (b, d) background sites. The unaccounted matter refers to the difference between the PM_2.5 gravimetric mass and the sum of the PM constituents (OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$, ${\mathrm{NH}}_{\mathrm{4}}^{+}$,Mineral dust and Cl⁻).

3.2 Chemical compositions of PM_2.5 in urban and background sites

3.2.1 Overview of PM_2.5 mass speciation

Figure 4 shows the annual average and seasonal average chemical compositions of PM_2.5 at six urban and six background sites, which represent the largest megacities and regional background areas of the NCP, YRD, PRD, TAR, NECR and SWCR. The chemical species of PM_2.5 in Shanghai were obtained from Zhao et al. (2015). The atmospheric concentrations of the main PM_2.5 constituents are also shown in Table 2. The EC, nitrate (NO${}_{\mathrm{3}}^{-})$, sulfate (${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$), ammonium (${\mathrm{NH}}_{\mathrm{4}}^{+}$) and chlorine (Cl⁻) concentrations were derived directly from measurements. Organic matter (OM) was calculated assuming an average molecular weight per carbon weight, showing an OC of 1.6 at the urban sites and 2.1 at the background sites, based on the work of Turpin and Lim (2001); however, these values are also spatially and temporally variable, and typical values could range from 1.3 to 2.16 (Xing et al., 2013). The calculation of mineral dust was performed on the basis of crustal element oxides (Al₂O₃, SiO₂, CaO, Fe₂O₃, MnO₂ and K₂O). In addition, the Si content, which was not measured in this study, was calculated based on its ratio to Al in crustal materials (Mason, 1966), namely [Si] = 3.41 × [Al]. Finally, the unaccounted-for mass refers to the difference between the PM_2.5 gravimetric mass and the sum of the PM constituents mentioned above.

The PM constituents' relative contributions to the PM mass are independent of their dilutions and reflect differences in the sources and processes controlling the aerosol compositions (Putaud et al., 2010). When all the main aerosol components except water are quantified, they account for 73.6–84.8 % of the PM_2.5 mass (average 79.2 %) at urban sites and for 76.2–91.1 % of the PM_2.5 mass (average 83.4 %) at background sites. The remaining unaccounted-for mass fraction may be the result of analytical errors, a systematic underestimation of the PM constituents with concentrations that are calculated from the measured data (e.g. OM, and mineral dust), and aerosol-bound water (especially when mass concentrations are determined at RH > 30 %). For the urban sites, the mean composition given in descending concentrations is 26.0 % OM, 17.7 % ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, 11.8 % mineral dust, 9.8 % ${\mathrm{NO}}_{\mathrm{3}}^{-}$, 6.6 % ${\mathrm{NH}}_{\mathrm{4}}^{+}$, 6.0 % EC and 1.2 % Cl⁻. For the background sites, the mean composition given in descending concentrations is 33.2 % OM, 17.8 % ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, 10.1 % mineral dust, 8.7 % ${\mathrm{NH}}_{\mathrm{4}}^{+}$, 8.6 % ${\mathrm{NO}}_{\mathrm{3}}^{-}$, 4.1 % EC and 0.9 % Cl⁻. Generally, the chemical compositions of PM_2.5 at background sites are similar to those of the urban sites, although they show a much higher fraction of OM and lower fractions of ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and EC. Significant seasonal variations of the chemical compositions were observed at urban sites (Fig. 4c), with much higher fractions of OM (33.7 %) and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (11.1 %) in the winter and much lower fractions of OM (20.7 %) and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (6.9 %) in the summer. In contrast, the fraction of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ was consistent among the different seasons, although its absolute concentration in the winter (14.9 µg m⁻³) was higher than that in the summer (11.7 µg m⁻³). Compared with those at urban sites, different seasonal variation of OM were observed at the background sites, which showed summer maxima and winter–spring minima (Fig. 4d). While the wintertime peaks of OM at the urban sites were probably due to additional local emission sources related to processes like heating, the summer peaks at the background sites were attributed to the enhanced biogenic emissions. Note that the seasonal variations of ${\mathrm{NO}}_{\mathrm{3}}^{-}$ were similar to those at urban sites; this phenomenon is due to the favourable conditions of cold temperatures and high relative humidity conditions leading to the formation of particulate nitrate. The seasonal behaviour of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ at the background sites were markedly different to those of the urban sites and indicates very different sources and atmospheric processing of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, which will be further discussed for specific regions of China.

There are significant variations of the absolute speciation concentrations at these urban and background sites (Table 2). For the urban sites, the OM concentrations span a 2-fold concentration range from 12.6 µg m⁻³ (Lhasa) to 23.3 µg m⁻³ (Shenyang), while these values range from 3.4 µg m⁻³ (Namtso) to 21.7 µg m⁻³ (Lin'an) at the background sites. The ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ concentrations exhibit larger spatial heterogeneities than those of the OM for both urban and background sites. The absolute values of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ have an approximately 25-fold range at urban sites, from 0.8 µg m⁻³ (Lhasa) to 19.7 µg m⁻³ (Chongqing), while this value has a 30-fold range at the background sites, from 0.4 µg m⁻³ (Namsto) to 11.2 µg m⁻³ (Lin'an). The corresponding mass fractions are 26.8 % in Chongqing and below 3 % in Lhasa. Much higher fractions of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ in PM_2.5 were observed at the urban sites located in southern China than those in northern China, although the average concentration of PM_2.5 is greater in the north than in the south, suggesting that sulfur pollution remains a problem for southern China (L. Liu et al., 2016). This problem may be attributed to a higher sulfur content of the coal in southern China, with 0.51 % in the north vs. 1.32 % in the south and up to > 3.5 % in Chongqing in southern China (Lu et al., 2010; Zhang et al., 2010). In addition, the higher fraction of sulfate in southern China is also likely associated with the higher oxidation capacity in southern China and therefore higher formation efficiency from SO₂ to ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$. The absolute values of ${\mathrm{NO}}_{\mathrm{3}}^{-}$ have an approximately 20-fold range at urban sites and a greater than 100-fold range at background sites. This heterogeneity reflects the large spatial and temporal variations of the NO_x sources. For the urban sites, the absolute EC values have a 5-fold concentration range, from 1.4 µg m⁻³ (Lhasa) to greater than 7.0 µg m⁻³ (Guangzhou), while this species has a 15-fold concentration range at the background sites and is mainly from anthropogenic sources. In comparison, the absolute concentrations of mineral dust exhibit much weaker spatial variations at the urban and background sites.

Figure 5 Average chemical composition of PM_2.5 at individual sites during (a) the entire period and (b–e) the individual seasons. The unaccounted matter refers to the difference between the PM_2.5 gravimetric mass and the sum of the PM constituents (OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$, ${\mathrm{NH}}_{\mathrm{4}}^{+}$,Mineral dust and Cl⁻). The site codes related to the observation stations can be found in Table 1.

The characteristics of the PM_2.5 chemical compositions at individual sites were discussed in more detail. In this section, six pairs of urban and background sites from each region of China were selected, and differences in the chemical compositions at urban and background sites were analysed.

3.2.2 North China Plain

Beijing is the capital of China and has attracted considerable attention due to its air pollution (Chen et al., 2013). Beijing is the largest megacity in the NCP, which is surrounded by the Yanshan Mountains to the west, north and north-east and is connected to the Great North China Plain to the south. The filter sampler is located in the courtyard of the Institute of Atmospheric Physics (IAP) (39.97^∘ N, 116.37^∘ E), 8 km north-west of the centre of downtown. The PM_2.5 concentration during the filter sampling period was 71.7 µg m⁻³, which is close to the 3-year average PM_2.5 value reported by TEOM (Table 1). PM_2.5 in Beijing is mainly composed of OM (26.6 %), SO${}_{\mathrm{4}}^{\mathrm{2}-}$ (16.5 %) and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (13.0 %) (Fig. 5a), which compare well with previous studies (Yang et al., 2011; Oanh et al., 2006). However, the mineral dust fraction found in this study (6.5 %) was much lower than that found in Yang et al. (2011) (19 %) but was comparable to that found in Oanh et al. (2006) (5 %), potentially due to a difference in definition. In addition, the EC fraction (5.7 %) was slightly lower than those found in previous studies (7–7.4 %) (Yang et al., 2011; H. B. Wang et al., 2015). The annual concentration of OM (19.1 µg m⁻³) in Beijing was comparable to those in Shanghai, Guangzhou and Chongqing but was much lower than that in Shenyang. Higher fractions of OM were observed in the winter (34.2 %) and autumn (30.5 %) than in the summer (21.6 %) and spring (20.9 %). The annual concentration of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (11.9 µg m⁻³) was much lower than in earlier years (15.8 µg m⁻³, 2005–2006) (Yang et al., 2011), suggesting that the energy structure adjustment implemented in Beijing (e.g. replacing coal fuel with natural gas) has been effective in decreasing the particulate sulfate in Beijing. Further support for this comes from the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ concentration in the winter (16.5 µg m⁻³), which is comparable to that in the summer (13.4 µg m⁻³). The significant ${\mathrm{NO}}_{\mathrm{3}}^{-}$ value (9.3 µg m⁻³) reflects the significant urban NO_x emissions in Beijing, which was greatest during the winter, as expected from ammonium-nitrate thermodynamics. The greater mineral component in the spring reflects the regional natural dust sources.

The filter sampling site in Xinglong (40.39^∘ N, 117.58^∘ E) was located at Xinglong Observatory, National Astronomical Observatory, Chinese Academy of Sciences, which is 110 km north-east of Beijing (Fig. 1). This site is surrounded by mountains and is minimally affected by anthropogenic activities. The PM_2.5 concentration during the filter sampling period was 42.6 µg m⁻³, which is close to the 3-year average PM_2.5 values reported by TEOM (Table 1). The annual chemical composition of PM_2.5 in Xinglong was similar to that in Beijing, although relatively higher fractions of OM and sulfate were observed in Xinglong (Fig. 5a). Higher fractions of OM were found in the winter (36.7 %) and higher fractions of sulfate were found in the summer (32.1 %) than in any other season (OM: 23.0–30.4 %; ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$: 15.7–20.1 %). Interestingly, the summer ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ concentration in Xinglong (14.4 µg m⁻³) was even higher than that in Beijing, suggesting spatially uniform distributions of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ concentrations across the NCP. This result indicates that regional transport can be an important source of SO${}_{\mathrm{4}}^{\mathrm{2}}$ aerosols in Beijing, especially during the summer.

3.2.3 Yangtze River delta

Shanghai is the economic centre of China, lying on the edge of the broad flat alluvial plain of the YRD, with a few mountains to the south-west. The filter sampler was located on top of a four-storey building of the East China University of Science and Technology (121.52^∘ E, 31.15^∘ N) (Zhao et al., 2015), approximately 10 km north-west of the centre. The PM_2.5 concentration during the filter sampling period was 68.4 µg m⁻³, which is greater than the 3-year average PM_2.5 value reported by EBAM, likely due to the different sampling periods (Table S1). The PM_2.5 in Shanghai mainly comprises OM (24.9 %), ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (19.9 %) and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (17.4 %), which is comparable to the results of previous studies (Ye et al., 2003; Wang et al., 2016). This site had the highest ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (11.9 µg m⁻³) and the second-highest ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (13.6 µg m⁻³) values at urban sites, while its OM value (17.1 µg m⁻³) was comparable to those of Guangzhou and Chongqing. The ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ values were highest during the autumn as expected based on the widespread biomass burning in the autumn in the YRD (Niu et al., 2013). However, the OM values were highest during the winter and mainly originated from secondary aerosol processes based on the highest OC∕EC ratios (6.0) and the poor relationship between OC and EC in this season.

Filter sampling was conducted at the Lin'an Regional Atmospheric Background Station (30.30^∘ N, 119.73^∘ E), which is a background monitoring station for the World Meteorological Organization (WMO) global atmospheric observation network. The Lin'an site was located on the outskirts of Lin'an County within Hangzhou Municipality, which was 200 km south-west of Shanghai (Fig. 1). This site is surrounded by agricultural fields and woods and is less affected by urban, industrial and vehicular emissions (Xu et al., 2017). The PM_2.5 concentration during the filter sampling period was 66.3 µg m⁻³, which is higher than the 3-year average PM_2.5 values reported by TEOM, likely due to the different sampling periods (Table S1). The annual chemical composition of the PM_2.5 in Lin'an was different to that in Shanghai, with much higher fractions of OM (32.7 %) and ${\mathrm{NH}}_{\mathrm{4}}^{+}$ (11.0 %). Furthermore, the absolute concentration of OM in Lin'an was much higher than that in Shanghai, especially in the summer (21.7 vs. 9.9 µg m⁻³), which may be attributed to the enhanced biomass burning at both local and regional scales as well as the higher concentration of summer EC in Lin'an than in Shanghai (2.2 vs. 1.4 µg m⁻³). In addition, the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ concentrations in Lin'an were comparable to those in Shanghai. These results suggest a spatially homogeneous distribution of secondary aerosols over the PRD and the transportation of aged aerosol and gas pollutants from urban areas has significantly changed the aerosol chemistry in the background area of this region.

3.2.4 Pearl River delta

Guangzhou is the biggest megacity in southern China located in the PRD and mainly consists of floodplains within the transitional zone of the East Asian monsoon system (Yang et al., 2011). The filter sampler was set up on the rooftop of a 15 m high building of the Guangzhou Institute of Geochemistry, Chinese Academy of Sciences (23.12^∘ N, 113.35^∘ E). This site was surrounded by heavily trafficked roads and dense residential areas, representing a typical urban location. The PM_2.5 concentration during the filter sampling period was 75.3 µg m⁻³, which is much higher than the 3-year average PM_2.5 value reported by EBAM (Table 1), likely due to the different sampling period and location. The PM_2.5 in Guangzhou mainly comprises OM (22.2 %), ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (17.3 %) and mineral dust (9.7 %), which have values comparable to previous studies conducted in the years 2013–2014 (Chen et al., 2016; Tao et al., 2017). This site has the lowest OC∕EC ratio (1.5) of all urban sites, which can be explained by the abundance of diesel engine trucks in Guangzhou (Verma et al., 2010). Obvious seasonal variations of OM, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ were observed, showing winter–autumn maxima and summer–spring minima. In addition, summer minima were also observed for EC and ${\mathrm{NH}}_{\mathrm{4}}^{+}$. High mixing heights in the summer and clean air masses affected by summer monsoons from the South China Sea should lead to the minima of these species in summer, while low wind speeds, weak solar radiation, relatively low precipitation (Tao et al., 2014) and relatively high emissions (Zheng et al., 2009) result in much higher concentrations of OM and secondary inorganic aerosols (${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and ${\mathrm{NH}}_{\mathrm{4}}^{+}$) in the winter and autumn.

Filter sampling was conducted at Dinghu Mountain station (23.15^∘ N, 112.50^∘ E), which is located in the middle of Guangdong Province in southern China. This site was surrounded by hills and valleys, and was approximately 70 km west of Guangzhou (Fig. 1). The PM_2.5 concentration during the filter sampling period was 40.1 µg m⁻³, close to the 3-year average PM_2.5 values reported by TEOM. Distinct seasonal variations of OM, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and ${\mathrm{NH}}_{\mathrm{4}}^{+}$ were observed, with the highest concentrations of OM and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ occurring in the winter, while the highest concentrations of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$and ${\mathrm{NH}}_{\mathrm{4}}^{+}$ occurred in the autumn. In contrast, EC and mineral dust showed weak seasonal variations. Dinghu Mountain has the second-highest EC and ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ values at background sites, at 2.0 and 10.1 µg m⁻³. In addition, the lowest OC∕EC ratio was observed at Dinghu Mountain (2.8); the other background sites had values ranging from 3.5 to 8.3. These results indicate that this background site is intensely influenced by vehicular traffic, fossil fuel combustion and industrial emissions due to the advanced urban agglomeration in the PRD region. These results are consistent with findings from previous studies (Liu et al., 2011; Wu et al., 2016). Compared with those from Guangzhou, higher fractions of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ were observed at Dinghu Mountain, while the fractions of OM and mineral dust were similar at these two sites, possibly indicating that there was a significantly larger fraction of transported secondary aerosols or aged aerosols at the background site of the PRD.

3.2.5 Tibetan Autonomous Region

Located in the inland TAR, Lhasa is one of the highest cities in the world (at an altitude of 3700 m). The city of Lhasa is located in a narrow west–east-oriented valley in the southern part of the TAR. The filter sampler was located on the roof of a 20 m high building on the campus of the Institute of Tibetan Plateau Research (Lhasa branch) (29.63^∘ N, 91.63^∘ E). This site is close to Jinzhu Road, one of the busiest roads in the city (Cong et al., 2011). The PM_2.5 concentration during the filter sampling period was 36.4 µg m⁻³, which is close to the 3-year average PM_2.5 values reported by TEOM. The PM_2.5 in Lhasa mainly comprises OM (34.5 %) and mineral dust (31.9 %), and the secondary inorganic aerosols (${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and ${\mathrm{NH}}_{\mathrm{4}}^{+}$) contributed little to the PM_2.5 (< 5 %). These results are comparable to those of a previous study conducted in the years 2013–2014 (Wan et al., 2016). In addition, this site reports the lowest OM (12.6 µg m⁻³), secondary inorganic aerosols (1.7 µg m⁻³) and EC (1.4 µg m⁻³) values of the urban sites in this study. Higher fractions of OM were observed in the winter (48.4 %) and spring (43.1 %), exceeding those in the summer (24.6 %) and autumn (31.2 %). Weak seasonal variations were found for the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (1.5–3.0 %) and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (1.1–1.7 %) values, suggesting negligible contributions from fossil fuel combustion in Lhasa.

Filter sampling was conducted at the Namtso Monitoring and Research Station for Multisphere Interactions (30.77^∘ N, 90.98^∘ E), a remote site located on the northern slope of the Nyainqentanglha Mountains, approximately 125 km north-west of Lhasa (Fig. 1). The PM_2.5 concentration during the filter sampling period was 9.5 µg m⁻³, which is close to the 3-year average PM_2.5 value reported by TEOM. The PM_2.5 at Namtso mainly comprises mineral dust (40.8 %) and OM (36.3 %), while ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ contributed less than 5 % to the PM_2.5. This chemical composition is distinctly different from those of the other background sites in this study but is comparable to the background site at Qinghai Lake in the TAR (N. N. Zhang et al., 2014). Namtso has the lowest OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and ${\mathrm{NH}}_{\mathrm{4}}^{+}$ values of all the background sites in this study. Spring maxima and winter minima were observed for the OM and EC, while the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and ${\mathrm{NH}}_{\mathrm{4}}^{+}$ values showed weak seasonal variations. The highest OC∕EC ratio was observed (8.3) at this site, suggesting that the organic aerosols at Namtso mainly originated from secondary aerosol processes or aged organic aerosols from regional transport.

3.2.6 North-east China region

Shenyang is the capital city of Liaoning province and the largest city in North-east China. The main urban area is located on a delta to the north of the Hun River. The filter sampler was located at the Shenyang Ecological Experimental Station of the Chinese Academy of Science (41.50^∘ N, 123.40^∘ E) and was surrounded by residential areas with no obvious industrial pollution sources around the monitoring station, representing the urban area of Shenyang. The PM_2.5 concentration during the filter sampling period was 81.8 µg m⁻³, which is close to the 3-year average PM_2.5 value reported by TEOM (Table 1). The PM_2.5 in Shenyang mainly comprises OM (28.5 %), ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (16.1 %) and mineral dust (11.3 %). This site reports the highest OM (23.3 µg m⁻³) and mineral dust (9.2 µg m⁻³) values as well as the second-highest EC (5.2 µg m⁻³) value of the urban sites. The ${\mathrm{NO}}_{\mathrm{3}}^{-}$ concentration at this site, however, was the second-lowest of the urban sites (Table 2). Much higher fractions of OM were observed in the winter (40.5 %) than in the other seasons (15.6–26.5 %) (Fig. 5), possibly due to the enhanced coal burning for winter heating. Further support for this pattern comes from the high abundance of chlorine during the cold seasons, which is mainly associated with coal combustion. The contribution from sea-salt particles is not important since the sampling sites are at least 200 km from the sea. Note that the fraction of ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ in the PM_2.5 during the winter was lower than that in the summer, although the absolute concentration was much higher in the winter (23.6 µg m⁻³) than in the summer (11.3 µg m⁻³). This result may be attributed to the reduced transformation of sulfur dioxide at low temperatures.

Filter sampling was conducted at the Changbai Mountain forest ecosystem station (42.40^∘ N, 128.01^∘ E), which was mostly surrounded by hills and forest and is located approximately 390 km north-east of Shenyang (Fig. 1). This site is situated 10 km from the nearest town, Erdaobaihe, which has approximately 45 000 residents. The sources of PM were expected to be non-local. Hence, this site is considered a background site in the NECR. The PM_2.5 concentration during the filter sampling period was 23.3 µg m⁻³, which is close to the 3-year average PM_2.5 value reported by TEOM (Table 1). The main contributions to PM_2.5 at Changbai Mountain were OM (38.1 %), mineral dust (16.0 %) and ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (14.3 %), similarly to those in Shenyang. Note that the summer OM concentrations were quite similar at these two sites (8.0 vs. 9.0 µg m⁻³), but the OC∕EC ratios were different (4.8 vs. 1.6), which may reflect the different origins of the OM at the urban (primary emissions) and background sites (secondary processes) of the NECR. The OM concentrations in the other seasons were much lower at Changbai Mountain than those from Shenyang city, especially during the winter (10.8 vs. 59.4 µg m⁻³). In fact, weak seasonal variations of chemical species (OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$ and NH${}_{\mathrm{4}}^{+})$ were observed at Changbai Mountain. This site reports the second-lowest values of OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ and Cl⁻ of the background sites. These results suggest that aerosols at Changbai Mountain were influenced by regional transport alone.

3.2.7 South-west China region

Chongqing is the fourth municipality near central China and lies on the Yangtze River in mountainous south-western China, near the eastern border of the Sichuan Basin and the western border of central China. For topographic reasons, Chongqing has some of the lowest wind speeds in China (annual averages of 0.9–1.6 m s⁻¹ from 1979 to 2007; Chongqing Municipal Bureau of Statistics, 2008), which favours the accumulation of pollutants. The filter sampler was located on the rooftop of a 15 m high building on the campus of the Southwest University (29.59^∘ N, 106.54^∘ E). This site is located in an urban district of Chongqing with no obvious industrial pollution sources around the monitoring site, representing the urban area of Chongqing. The PM_2.5 concentration during the filter sampling period was 73.5 µg m⁻³, of which 26.8 % is ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, 23.5 % is OM, 10.0 % is mineral dust, 8.9 % is ${\mathrm{NO}}_{\mathrm{3}}^{-}$, 8.2 % is EC and 6.5 % is ${\mathrm{NH}}_{\mathrm{4}}^{+}$. The OM fraction is smaller than those measured by Yang et al. (2011) (32.7 %) and Chen et al. (2017) (30.8 %), while the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ fraction is greater than the values reported in these two studies (19.8–23.0 %). This site shows the highest ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (19.7 µg m⁻³), the highest ${\mathrm{NH}}_{\mathrm{4}}^{+}$ (6.1 µg m⁻³) and the third-highest EC (4.8 µg m⁻³) values of the urban sites. Weak seasonal variation in the chemical composition of PM_2.5 was observed, although a much higher concentration of this species was found in the winter than in the other seasons.

Filter sampling took place at the Gongga Mountain Forest Ecosystem Research Station (29.51^∘ N, 101.98^∘ E) in the Hailuogou Scenic Area, a remote site located in southeastern Ganzi in the Tibetan Autonomous Prefecture in Sichuan province. This site is mostly surrounded by glaciers and forests and is located approximately 450 km north-west of Chongqing (Fig. 1). The PM_2.5 concentration during the filter sampling period was 32.2 µg m⁻³, close to the 3-year average PM_2.5 value reported by TEOM (Table 1). The dominant components of PM_2.5 were OM (40.7 %), ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$(14.6 %) and mineral dust (9.8 %), similarly to those at Changbai Mountain. This site has the second-highest OM (13.1 µg m⁻³) value of the background sites, which may mainly be due to secondary processes, considering the high OC∕EC ratio (5.6). In addition, distinct seasonal variations of OM were observed, which show summer maxima (19.9 µg m⁻³) and autumn minima (9.1 µg m⁻³). Previous studies showed higher mixing ratios of the VOCs during the spring and summer and lower mixing ratios during autumn at Gongga Mountain (J. K. Zhang et al., 2014), which may result in high concentrations of OM in the summer because the OC∕EC ratio reaches its highest value in the summer (10.3). The second-lowest EC and ${\mathrm{NO}}_{\mathrm{3}}^{-}$ values of the background sites were observed here, suggesting the insignificant influence of human activities in this region.

3.3 Temporal evolution and chemical composition PM_2.5 on polluted days

3.3.1 Temporal evolution of PM_2.5 mass concentration on polluted days

Using the Ambient Air Quality Standard (GB3095-2012) of China (CAAQS), the occurrences of polluted days exceeding the daily threshold values during 2012–2014 were counted for each site (Fig. 6). Based on the number of polluted days exceeding the CAAQS daily guideline of 35 µg m⁻³, substandard days of PM_2.5 account for more than 60 % of the total period at the majority of urban sites, except Lhasa, Taipei and Sanya. Note that the 10 most polluted cities (Ji'nan, Chengdu, Taiyuan, Hefei, Shenyang, Xi'an, Changsha, Shijiazhuang, Wuxi and Chongqing) experienced less than 20 % on clean days (daily PM_2.5 < 35 µg m⁻³) during the 3-year observation period. Interestingly, the occurrences of heavily polluted days (daily PM_2.5 > 150 µg m⁻³) were different among these 10 most polluted cities. While more than 15 % of the total period comprised heavily polluted days in Ji'nan, Taiyuan, Chengdu, Xi'an and Shijiazhuang, heavily polluted days accounted for less than 5 % of the total days in the other five cities, which mainly experienced slightly polluted (35–75 µg m⁻³) and moderately polluted (75–115 µg m⁻³) days. Due to the regional pollutant transport, the rural and background sites near the most polluted cities also showed high occurrences of polluted days. Polluted days accounted for more than 50 % of the total period at Xin'long, Lin'an and Dinghu Mountain. In addition, an even higher occurrence of polluted days (> 80 %) was found for the rural areas of Yucheng and Xianghe. In contrast, the background sites in the TAR, NECR and SWCR rarely experienced polluted days, and over 80 % of the total period comprised clean days at these sites.

Figure 6 Days separated by the threshold values of the Ambient Air Quality Standard (AAQS) (GB3095-2012) of the Chinese guidelines. The threshold values of 35, 75, 115 and 150 µg m⁻³ used for the daily concentration ranges are represented as clean (< 35 µg m⁻³), slightly polluted (35–75 µg m⁻³), moderated polluted (75–115 µg m⁻³), polluted (115–150 µg m⁻³) and heavily polluted (> 150µg m⁻³), which was suggested by the AAQS guidelines. The site codes related to the observation stations can be found in Table 1.

Figure 7 Monthly distribution of the occurrence of the polluted days exceeding the Ambient Air Quality Standard (AAQS) (GB3095-2012) of China. The symbol size represents the occurrences of polluted days for the corresponding month. The coloured circles represent the different mass ranges. The sites of Nagri and Mount Everest are excluded because of the small sample size. The site codes related to the observation stations can be found in Table 1.

The polluted days were not equally distributed throughout the year. The monthly distributions for the polluted days at each site are shown in Fig. 7. In terms of the occurrences of heavily polluted days, December, January and February were the predominant months for the urban sites located in the most polluted areas of the GZP and NCP, where both the unfavourable dispersion conditions for pollutants and the additional emission enhancements from residential heating contributed to heavy pollution in the winter. The heavy pollution occurring in April and November in Cele was primarily caused by sandstorms and dust storms. Heavily polluted days were rarely observed at the 12 background sites in this study. The moderately polluted and polluted days were still mainly concentrated in the winter in the megacities of the GZP and NCP and also occurred in the winter in the megacities of the YRD and SWCR. In addition, March to June and September to October were periods with high occurrences of polluted days. Dust storms from northern China (March to April), biomass burning after crop harvests (May to June and September to October) and worsening dispersion conditions after the summers likely accounted for the polluted days (Cheng et al., 2014; Fu et al., 2014). The majority of slightly polluted days occurred from June to September, except at several urban sites in southern China. The mass level of 35–75 µg m⁻³ was considered a low level of pollution for the entire year, illustrating that the summer and early autumn experienced cleaner conditions.

3.3.2 Chemical evolution of PM_2.5 composition on polluted days

The mean percentile compositions of the major components in PM_2.5 at different pollution levels from four paired urban-background sites are shown in Fig. 8. While the pollution level increased from clean to moderately polluted, the EC fraction in Beijing decreased slightly, the OM fraction decreased significantly, and the sulfate and nitrate contributions increased sharply (Fig. 8a). The same chemical evolution of PM_2.5 was also observed at the background site of Xinglong, suggesting that regional transport plays a vital role in the formation of the slightly and moderately polluted days in the NCP. When the pollution level increased to heavily polluted, however, the OM fraction further increased and was accompanied by increases of the sulfate and nitrate contributions as well as decreases of the mineral dust contribution, indicating the enhanced secondary transformation of gaseous pollutants (e.g. SO₂, NO_x, VOCs) during heavily polluted periods (Z. R. Liu et al., 2016). Note that a steady increase in $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ ratio was observed with the aggravation of pollution (Fig. 8a), suggesting the relatively more important contribution of mobile than stationary sources (Arimoto et al., 1996). In addition, much higher OC∕EC ratios were found in Beijing, especially during the heavily polluted days (OC∕EC = 6.3) (Fig. 8), compared with Guangzhou, Shenyang and Chongqing. Higher OC∕EC ratios have been reported to be emitted from coal combustion (2.7) and biomass burning (6.6) than from motor vehicles (1.1) (Watson et al., 2001; Saarikoski et al., 2008). In northern China, the residential sector is the largest emitter of carbonaceous aerosols (Lei et al., 2011; Lu et al., 2011), which are formed by the inefficient combustion of fossil fuel and biomass in unregulated cooking and heating devices. For OC, the residential sector contribution can exceed 95 % (J. Liu, et al., 2016). Thus, the highest OC∕EC ratio in Beijing indicates that residential emissions would also contribute considerably to the development of heavily polluted days.

Figure 8 Average chemical composition of PM_2.5 and mass ratio of $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ and OC∕EC with respect to pollution level. The C, SP, MP and HP are related to clean (daily PM_2.5 < 35 µg m⁻³), slightly polluted (35 µg m⁻³ < daily PM_2.5 < 75 µg m⁻³), moderated polluted (75 µg m⁻³ < daily PM_2.5 < 150 µg m⁻³) and heavily polluted (daily PM_2.5 > 150 µg m⁻³) levels. The unaccounted matter refers to the difference between the PM_2.5 gravimetric mass and the sum of the PM constituents (OM, EC, ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$, ${\mathrm{NO}}_{\mathrm{3}}^{-}$, ${\mathrm{NH}}_{\mathrm{4}}^{+}$, Mineral dust and Cl⁻).

Unlike in Beijing, the contributions of OM and EC were almost constant across the different pollution levels in Guangzhou, while the contribution of the secondary inorganic aerosols (SIAs) increased slightly (Fig. 8b). Interestingly, the nitrate contribution increased faster than that of the sulfate when the pollution level increased from clean to heavily polluted, similarly to the patterns in Beijing. Furthermore, the $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ ratio increased continuously and reported the highest ratio of $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ (1.3) during the heavily polluted days in Guangzhou (Fig. 8). At the same time, the ratio of OC∕EC was nearly constant with the aggravation of pollution, and it reported the lowest OC∕EC ratio (1.6–1.8) among the four megacities. These results suggest that the contribution of local traffic emissions was dominant in the development of fine-particulate pollution. The chemical evolution of PM_2.5 at the background site of PRD was similar to that of the urban site at Guangzhou, although a significant contribution of SIA was observed when the pollution level increased from clean to moderately polluted (34 % vs. 58 %). Note that the contribution of sulfate increased sharply, suggesting that regional transport dominated particle pollution during heavily polluted days.

Compared with Beijing, a reversed chemical evolution of PM_2.5 for the different pollution levels was observed in Shenyang, with the OM fraction increasing sharply from 22 to 37 %, while the SIA decreased slightly from 39 to 31 % (Fig. 8c). Note that a steady increase in sulfate from slightly polluted days to heavily polluted days was observed. In addition, a nearly constant low ratio of $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ (0.30–0.38) and continually increasing ratio of OC∕EC (2.3–4.5) was observed with the aggravation of pollution. These results suggest that enhanced local stationary emissions like coal combustion dominate the temporal evolution of PM_2.5 on polluted days in Shenyang. The higher concentration of Cl⁻ in Shenyang than in other cities in this study further supports the significant contribution of coal combustion. A similar chemical evolution of PM_2.5 was found at the background site of Changbai Mountain, which showed a significantly increased OM fraction and a slight decrease in SIA when the pollution level increased from clean to slighted polluted, indicating the enhanced contribution from local emissions like coal combustion for heating during slightly polluted days. Further support for this pattern is seen in the increase in the EC fraction (Fig. 8g).

Similarly to Guangzhou, the contribution of OM was almost constant for different pollution levels in Chongqing, while a much higher contribution of SIA was observed, especially on heavily polluted days. In addition, a steady increase in the $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ ratio was observed, similarly to those in Beijing and Guangzhou, suggesting that the contribution of mobile sources was relatively more important than stationary sources (Arimoto et al., 1996). Furthermore, the OC∕EC ratio also continually increased with the aggravation of pollution and was different in Guangzhou but similar to that in Shenyang. Note that the fraction of OM, sulfate and nitrate during the heavily polluted days in Chongqing was much higher than in Beijing, Guangzhou and Shenyang, suggesting the higher oxidation capacity and therefore higher formation efficiency from gaseous pollutants (e.g. SO₂, NO_x, VOCs) to secondary aerosol. These results highlight the importance of local traffic emissions and the formation of secondary aerosol in driving PM_2.5 pollution in Chongqing. The background site of Gongga Mountain shows lower contributions of OM, EC, SIA and mineral dust when the pollution level increased from clean to slightly polluted days, similarly to the pattern observed in Xinglong. Note that the unaccounted-for fraction was largely increased on slightly polluted days (33 % vs. 10 %), possibly due to the increase in aerosol-bound water related to the hygroscopic growth of aerosols at high RH values on slightly polluted days (Bian et al., 2014).

4 Conclusions

We have established a national-level network (CARE-China) that conducted continuous monitoring of PM_2.5 mass concentrations at 40 ground observation station, including 20 urban sites, 12 background sites and 8 rural/suburban sites. The average aerosol chemical composition was inferred from the filter samples from six paired urban and background sites, which represent the largest megacities and regional background areas in the five most polluted regions and the TAR of China. This study presents the first long-term data set including 3-year observations of online PM_2.5 mass concentrations (2012–2014) and 1-year observations of PM_2.5 compositions (2012–2013) from the CARE-China network. One of the major purposes of this study was to compare and contrast urban and background aerosol concentrations from nearby regions. The major findings include the following:

1. The average PM_2.5 concentration from 20 urban sites is 73.2 µg m⁻³ (16.8–126.9 µg m⁻³), which is 3 times greater than the average value of the 12 background sites (11.2–46.5 µg m⁻³). The highest PM_2.5 concentrations were observed at the stations on the Guanzhong Plain (GZP) and the NCP. PM_2.5 pollution is also a serious problem for the industrial regions of North-east China and the Sichuan Basin and is a relatively less serious problem for the YRD and the PRD. The background PM_2.5 concentrations of the NCP, YRD and PRD were comparable to those of the nearby urban sites, especially for the PRD. A distinct seasonal variability in PM_2.5 is observed, presenting peaks during the winter and minima during the summer at the urban sites, while the seasonal variations of PM_2.5 at the background sites vary in different part of China. Bimodal and unimodal diurnal variation patterns were identified at both the urban and background stations.

2. The major PM_2.5 constituents across all the urban sites are OM (26.0 %), ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ (17.7 %), mineral dust (11.8 %), ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (9.8 %), ${\mathrm{NH}}_{\mathrm{4}}^{+}$ (6.6 %), EC (6.0 %), Cl⁻ (1.2 %) at 45 % RH and unaccounted matter (20.7 %). Similar chemical compositions of PM_2.5 were observed for the background sites and were associated with higher fractions of OM (33.2 %) and lower fractions of ${\mathrm{NO}}_{\mathrm{3}}^{-}$ (8.6 %) and EC (4.1 %). Analysis of filter samples reveals that several PM_2.5 chemical components varied by more than an order of magnitude between sites. For urban sites, the OM ranges from 12.6 µg m⁻³ (Lhasa) to 23.3 µg m⁻³ (Shenyang), the ${\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}$ ranges from 0.8 µg m⁻³ (Lhasa) to 19.7 µg m⁻³ (Chongqing), the ${\mathrm{NO}}_{\mathrm{3}}^{-}$ ranges from 0.5 µg m⁻³ (Lhasa) to 11.9 µg m⁻³ (Shanghai) and the EC ranges from 1.4 µg m⁻³ (Lhasa) to 7.1 µg m⁻³ (Guangzhou). The PM_2.5 chemical species of the background sites exhibit larger spatial heterogeneities than those of the urban sites, suggesting different contributions from regional anthropogenic and natural emissions and from the long-range transport to background areas.

3. Notable seasonal variations of PM_2.5 polluted days were observed, especially for the megacities in east-central China, resulting in frequent heavy pollution episodes occurring during the winter. The increasing contribution of secondary aerosol on polluted days was observed both for the urban and nearby background sites, suggesting that fine-particle pollution in the most polluted areas of China assumes a regional tendency, and the importance of addressing the emission reduction of secondary aerosol precursors. In addition, the chemical species dominating the evolution of the heavily polluted events were different, while a decreasing or constant contribution of OM associated with an increasing contribution of SIA characteristic evolution of PM_2.5 in NCP, PRD and SWCR. The opposite phenomenon was observed in NECR. Further analysis from the $\left[{\mathrm{NO}}_{\mathrm{3}}^{-}\right]/\left[{\mathrm{SO}}_{\mathrm{4}}^{\mathrm{2}-}\right]$ ratio and OC∕EC ratio showed that fine-particle pollution in Guangzhou and Shenyang was mainly attributed to the traffic emissions and coal combustion, respectively, while more complex and variable major sources including mobile vehicle emission and residential sources contributed to the development of heavily polluted days in Beijing. As for Chongqing, the higher oxidation capacity suggested more attention should be paid to the emission reduction of secondary aerosol precursors. These results suggest different formation mechanisms of the heavy pollution in the most polluted city clusters, and unique mitigation measures should be developed for different regions of China.

   The seasonal and spatial patterns of urban and background aerosols emphasize the importance of understanding the variabilities of the concentrations of major aerosol species and their contributions to the PM_2.5 budget. Comparisons of PM_2.5 chemical compositions from urban and background sites of adjacent regions provided meaningful insights into aerosol sources and transport and into the role of urban influences on nearby rural regions. The integration of data from 40 sites from the CARE-China network provided an extensive spatial coverage of fine-particle concentrations near the surface and could be used to validate model results and implement effective air pollution control strategies.