Characterization, Long-range Transport and Source Identification of Carbonaceous Aerosols during Spring and Autumn Periods at a High Mountain Site in South China

PM 10 (particulate matter) samples were collected at Mount Lu, a high elevation mountain site in south China (August and September of 2011; and March, April and May of 2012). Eight carbonaceous fractions of particles were analyzed to characterize the possible carbonaceous emission sources. During the sampling events, daily average concentrations of PM 10 at Mount Lu were 97.87 µg/m 3 and 73.40 µg/m 3 in spring and autumn, respectively. The observed mean organic carbon (OC) and element carbon (EC) concentrations during spring in PM 10 were 10.58 µg/m 3 and 2.58 µg/m 3 , respectively, and those in autumn were 6.89 µg/m 3 and 2.40 µg/m 3 , respectively. Secondary organic carbon concentration was 4.77 µg/m 3 and 2.93 µg/m 3 on average, accounting for 28.0% and 31.0% of the total OC in spring and autumn, respectively. Relationships between carbonaceous species and results of principal component analysis showed that there were multiple sources contributing to the carbonaceous aerosols at the observation site. Through back trajectory analysis, it was found that air masses in autumn were mainly transported from the south of China, and these have the highest OC but lowest EC concentrations. Air masses in spring transported from northwest China bring 7.77 µg/m 3 OC and 2.28 µg/m 3 EC to the site, with lower levels coming from other sites. These air mass sources were featured by the effective carbon ratio (ECR).


Introduction
Carbonaceous aerosol, comprised of organic and elemental carbon (OC and EC), is ubiquitous in the Earth's atmosphere [1,2].OC and EC in suspended particulate matter (PM) play important roles in visibility, climate and health effects [3].EC, which is often equated with optically-derived and light-absorbing black carbon, is mainly emitted from anthropogenic combustion sources.There are two existing forms of particulate OC, namely primary OC (POC) and secondary OC (SOC).POC is directly emitted into the atmosphere, while SOC is formed through atmospheric oxidation of reactive organic gases and subsequent gas-to-particle conversion processes [4][5][6].In urban air, second organic aerosol (SOA) accounted for 30%-60% of the OA; while in rural air and the free troposphere, it accounted for more than 70% of the OA [7].
In last several decades, carbonaceous aerosols from anthropogenic emissions in Asia are increasing [5,8], and China is one of the biggest emissions contributors, accounting for over 50% of the total emission of carbonaceous pollutants in Asia [2].A few studies on carbonaceous aerosols have been conducted in developed urban areas in China [9], such as Beijing [10,11], Tianjin [5,12] and the Pearl River Delta Region (PRDR) [13,14], while observations of carbonaceous aerosols in mountain regions are very limited.Mount Lu is located at an altitude of 1165 m A.S.L. (above sea level) in South China.The summit of Mount Lu could perform as a special site representing the regional pollution conditions, and it is appropriate to estimate both the source of aerosols and aerosol characteristics in the free troposphere [2].Therefore, in this study, concentrations of OC and EC in PM 10 were measured in spring and autumn at Mount Lu.The objectives of this study were (1) to characterize the concentrations and temporal variations of organic carbon and element carbon in the PM 10 at the high elevation, and (2) to estimate SOC concentration and examine the possible source apportionment of carbonaceous aerosols in the region.

Sampling
Mount Lu, covering an area of 300 km 2 , is situated to the north of Jiangxi Province.It is one of the most renowned mountains in the country.Two developed regions, namely PRDR and the Yangtze River Delta Region (YRDR), are about 700 km to the southwest and 400 km to the northeast of the mountain, respectively.The Guling town, with a population of about ten thousand, is situated on the top of Mount Lu.This mountain area is essentially free from local pollution.This is because most residents in the town work in tourism and its related services.
A total of 68 PM 10 samples were collected in August and September, 2011 and from March to May, 2012 at a meteorological station (29 • 35 N, 115 • 59 E, 116 m A.S.L.) established in the year of 1954 at the summit of Mount Lu (Figure 1).PM 10 samples were collected on quartz fiber filters (Pall Corporation, New York, USA, pre-fired at 450 • C for 6 h) by a medium volume air sampler (TH-150C, Tianhong Intelligent Instrument Plant of Wuhan, China), operating at a flow rate of 100 L/min for 23 h daily (from 9 a.m. to 8 a.m.).After sampling, each sample was separately wrapped with aluminum foil and stored at 4 • C before analysis conducted within 15 days.
The carbon that evolves at each temperature is oxidized to carbon dioxide (CO 2 ) and then reduced to methane (CH 4 ) for quantification with a flame ionization detector.As temperature increases in the inert helium, some of the organic carbon pyrolyzes to elemental carbon, resulting in darkening of the filter deposit.This darkening is monitored by reflectance of 633 nm light of an He-Ne laser.When oxygen is added, the original and pyrolyzed elemental carbon combusts and the reflectance increases.
The amount of carbon measured after oxygen is added until the reflectance achieves its original value is reported as optically detected pyrolyzed carbon (OPC).The eight fractions OC1, OC2, OC3, OC4, EC1, EC2, EC3, and OPC are reported separately in the data sheet.The IMPROVE protocol defines OC as OC1 + OC2 + OC3 + OC3 + OC4 + OPC and EC as EC1 + EC2 + EC3 − OPC [2,5,15].The analyzer was calibrated daily with known quantities of CH 4 .The detection limit of this method is 0.01 µg.Blank filters were collected similar to the protocol used for samples, in order to correct carbonaceous species.In addition, the ions of PM 10 samples were analyzed by Dionex IC (ionic composition)-2500 (Dionex, TX, USA).
Meteorological data for the sampling site during the sampling events were obtained from automatic weather system reports published by local meteorological station.
Atmosphere 2016, 7, 122 3 of 13 OC3, OC4, EC1, EC2, EC3, and OPC are reported separately in the data sheet.The IMPROVE protocol defines OC as OC1 + OC2 + OC3 + OC3 + OC4 + OPC and EC as EC1 + EC2 + EC3 − OPC [2,5,15].The analyzer was calibrated daily with known quantities of CH4.The detection limit of this method is 0.01 μg.Blank filters were collected similar to the protocol used for samples, in order to correct carbonaceous species.In addition, the ions of PM10 samples were analyzed by Dionex IC (ionic composition)-2500 (Dionex, TX, USA).Meteorological data for the sampling site during the sampling events were obtained from automatic weather system reports published by local meteorological station.

Temporal Variability
Daily concentrations of PM 10 at Mount Lu ranged from 33.60 to 193.74 µg/m 3 and 4.55 to 231.46 µg/m 3 , with an average of 97.87 µg/m 3 and 73.40 µg/m 3 in spring and autumn, respectively (Table 1).The concentrations of carbonaceous species showed pronounced temporal variability during the study period (August-September, 2011 and March-May, 2012).The maximum-to-minimum ratios for PM 10 were 145.54 and 13.45 for OC and EC, respectively.The higher variability for OC concentrations may be attributed to different emission sources [15].According to the previous studies, the average OC concentration emitted from coal combustion and biomass burning was 4.79 and 1.38 µg/m 3 , respectively.While the contribution of motor vehicle exhaust to OC can vary from 0.08 µg/m 3 to 22.25 µg/m 3 [16,17].In this study, concentrations of PM 10 , OC and EC in the samples collected in spring (average temperature: 12.13 • C) were 1.33, 1.5 and 1.07 times as high as those in the samples collected during fall (average temperature: 19.8 • C), indicating higher concentrations of carbon aerosols during the colder months.This pattern is consistent with our previous findings that higher concentrations of carbon aerosols were always found in the colder months.This phenomenon might be attributed to enhanced biomass burning, gasoline fuel and typical meteorological conditions (less efficient photochemical decomposition and lower inversion height) [5].Carbonaceous aerosol concentrations at Mount Lu were compared with other background sites (Table 2), and the results showed that the EC concentrations in PM 10 at Mount Lu were generally higher than that reported in Kathmandu, Nepal (1.5 µg/m 3 ) [18], Nagarkot, Nepal (0.94 µg/m 3 ) [18], Zhuzhang, China (0.34 µg/m 3 ) [19] and Shangri-La, China (0.34 µg/m 3 ) [20].In contrast, they were lower than those in Kaohsiung, Taiwan (6.1 µg/m 3 ) [21] and Hangzhou, China (4.06 µg/m 3 ) [22].
The origin of carbonaceous aerosols can be reflected by the relationship between OC and EC [23].In this study, OC and EC had similar temporal variations (Figures 2 and 3) and were well related to each other (Figures 4 and 5), indicating common emission sources and similar atmospheric processes shared by OC and EC during the observation period.It has been previously reported that an OC/EC ratio exceeding 2 or 2.2 indicated the presence of secondary organic aerosol [2,24].In this study, the average OC/EC ratios in PM 10 at Mount Lu were 3.91 and 3.27 in spring and autumn, respectively (Table 1), and these values were comparable to the OC/EC ratio in other sites listed in Table 2 and higher than 2.2, suggesting that SOC may have contributed largely to the carbonaceous aerosols at Mount Lu.The OC/EC ratios in this study were also higher than those observed in urban areas in China including Beijing (a ratio of 2.9), Shanghai (a ratio of 2.5) and PRDR (a ratio of 2.4) [13,25].

Estimation of SOC Concentrations
EC is relatively inert regarding its chemical reactions in atmosphere, and it is solely derived from primary emissions.Unlike EC, OC can be derived from both primary emissions and the chemical reactions occurring between gaseous organic precursor species and by the oxidation of volatile organic compounds [8].The direct measurement of SOC is unlikely to be carried out because they are derived from not only the various physical processes but also the chemical transformation processes.The EC-tracer method has been applied to estimate different fractions of SOC for various environments, such as rural, semi-urban and urban environments to evaluate the mass concentrations of SOC [23,27,28], and it is therefore adopted in the present study.The equation is as follows: where OCsec is the SOC; OCtot is the total organic carbon; and (OC/EC)pri is the primary ratio.The primary OC/EC ratios can be affected by many factors including temporal fluctuations, fluctuations in emissions, meteorology conditions, and thus the ratios vary among different sources.Therefore, the determination of the primary OC/EC values is crucial.In previous studies, the ratio of OC/EC in the lowest 5%-10% or below the threshold of 2.9 from the least-squares regression analysis was applied [29][30][31].In this study, the regression of the selected data suggested a primary OC/EC ratio of 2.06 and 3.08 in autumn and spring, respectively, which was comparable with the ratio (OC/EC = 2.19) at

Estimation of SOC Concentrations
EC is relatively inert regarding its chemical reactions in atmosphere, and it is solely derived from primary emissions.Unlike EC, OC can be derived from both primary emissions and the chemical reactions occurring between gaseous organic precursor species and by the oxidation of volatile organic compounds [8].The direct measurement of SOC is unlikely to be carried out because they are derived from not only the various physical processes but also the chemical transformation processes.The EC-tracer method has been applied to estimate different fractions of SOC for various environments, such as rural, semi-urban and urban environments to evaluate the mass concentrations of SOC [23,27,28], and it is therefore adopted in the present study.The equation is as follows: where OC sec is the SOC; OC tot is the total organic carbon; and (OC/EC) pri is the primary ratio.The primary OC/EC ratios can be affected by many factors including temporal fluctuations, fluctuations in emissions, meteorology conditions, and thus the ratios vary among different sources.Therefore, the determination of the primary OC/EC values is crucial.In previous studies, the ratio of OC/EC in the lowest 5%-10% or below the threshold of 2.9 from the least-squares regression analysis was applied [29][30][31].In this study, the regression of the selected data suggested a primary OC/EC ratio of 2.06 and 3.08 in autumn and spring, respectively, which was comparable with the ratio (OC/EC = 2.19) at Mount Tai in northern China [32].The estimated SOC concentrations varied from 0.10 to 25.38 µg/m 3 , with an average of 2.93 µg/m 3 in autumn and from 0.11 to 22.11 µg/m 3 , with an average of 4.77 µg/m 3 in spring.The average proportion of SOC to the total OC was 31% and 28% in the autumn and spring, respectively.Compared with SOC proportion in PM 2.5 samples (45.0%) in the same area, the average proportion for PM 10 in autumn was lower [2], indicating that SOC mainly enriched in fine particles.
As an important characteristic of particles, aerosol acidity can alter the uptake of precursors and the partitioning of volatile and semi-volatile compounds between the particle and gas phases, thereby affecting aerosol phase relations [2].In general, [H + ] strong (calculated as 2 × SO 4 2− + NO 3 was suggested to be an indicator of aerosol acidity.For PM 2.5 samples at Mount Lu in autumn, the average concentration of [H + ] strong was 52.7 nmol/m 3 , indicating that a general acidic state of the fine particles at Mount Lu.Furthermore, a good correlation between [H + ] strong and SOC suggested a dominant role of aerosol acidity in the formation of SOAs [2]. In this study, the data obtained during the special climate events like cloud/fog events and dust storms were excluded in the analysis of acidity.The concentrations of [H + ] strong ranged from 0.10 to 29.21 nmol/m 3 (with the mean of 4.57 nmol/m 3 ) in autumn and from 0.01 to 53.35 nmol/m 3 (with the mean value of 5.05 nmol/m 3 ) in spring.These values were 10 times lower than those in PM 2.5 samples, suggesting that the acidic material was mainly associated with fine particles.In addition, the correlation between SOC and [H + ] strong in this study was not as strong as that for PM 2.5 , indicating that reactions catalyzed by heterogeneous acid may have contributed to the formation of SOA in fine particles rather than coarse particles [8].

Source Apportionment of Carbonaceous Species
The ratio of EC/TC can differentiate the dominant contributors among fossil fuel burning and biomass burning.An EC/TC ratio between 0.1 and 0.2 indicates the source of carbonaceous species contributed by biomass burning, while a higher ratio (~0.5) suggests the source coming from fossil fuel combustion [33][34][35][36].In this study, the average EC/TC ratios of PM 10 were 0.18 and 0.25 in spring and autumn at Mount Lu, respectively, indicating that biomass burning was the main source of carbonaceous aerosols at the observation site.Similarly, in previous studies, biomass burning in open fire and residential consumption was suggested as one of the most important carbonaceous emission sources in China [2,12].
However, because of great variations in emission patterns in different countries, these ratios may not accurately reflect emission characteristics.Therefore, principal component analysis (PCA) was conducted for eight carbon fractions to further characterize the possible emission sources of carbonaceous aerosols at the observation site.
Results of PCA for samples collected in autumn and spring are summarized in Tables 3 and 4. For PM 10 autumn samples, and two factors accounted for 75.75% of the total variance in the data.Factor 1, explaining 46.12% of the variance, presented high loading for OC2, OC3, OC4, EC1 and OPC.Among these fractions, OC2 and OPC originated from coal combustion, and OC3, OC4 and EC1 represented gasoline-motor-vehicle exhaust.This factor appears to represent gasoline motor vehicle exhaust and coal combustion [37].Factor 2, which explained 29.63% of the variance, showed high loadings for OC1, EC2 and EC3.The high loading of OC1 in factor 2 reflected the contribution of biomass burning, and EC2 and EC3 were enriched in diesel-vehicle exhaust.Thus, factor 2 represented diesel vehicle exhaust and biomass burning.
In spring, three factors accounted for 87.07% of the total variance.Among these factors, factor 1 explained 47.51% of the variance, and it had high loading for OC2, OC3, OC4, EC1 and OPC.Similar to the fall results, Factor 1 in spring represents gasoline motor vehicle exhaust and coal combustion.Factor 2, which explained 20.48% of the variance, showed high loadings for EC2, EC3, from which the diesel-vehicle exhaust sources could be inferred [5].As for factor 3, the high loading of OC1 reflected the main contribution from biomass burning.

Long-Range Transport of Carbonaceous Aerosol
To better elucidate the origin and transport patterns for air mass samples, 72 h back trajectory was analyzed by the Hybrid Single Particle Lagrangian Integrated Trajectory (HYSPLIT) model with FNL (final analysis data) meteorological datasets at a height of 1165 m A.S.L. (above sea level) (Figures 6 and 7).Owing to the occurrence of scavenging in fog or cloud conditions, the trajectory analysis did not include the samples collected during fog or cloud periods.
In autumn, all the air masses can be classified into three categories, namely N/NE-air (north/northeast of China) masses, S-air (south of China) masses and E-air (east of China) masses.Among the three trajectory categories, the N/NE-air masses that originate from continental areas in northern and northeastern China crossed the Beijing-Tianjin-Hebei region and the Shandong province and finally reached the station; the S-air masses came from coastal areas in southern China and then crossed Guangdong before finally reaching the station; the E-air masses originated from coastal areas in the east part of China and then traveled to the station across Zhejiang and Fujian provinces.It is noteworthy that this paper has omitted the air masses associated with trajectory that passed over two regions.
concentrations in descending order was E-air masses (3.01 μg/m 3 ) > N/NE-air masses (2.70 μg/m 3 ) > S-air masses (1.99 μg/m 3 ).The fact beyond expectation is that S-air masses had the highest OC concentration, which was an average of 8.01 μg/m 3 .As they always came from the sea and were relatively clean, their EC concentration was the lowest.However, compared with the YRDR and northern China, the rapidly developing PRDR situated in the air mass pathway owns a different industrial structure, and the famous ozone and NOX pollution there could favor the formation of SOA [2,38], and the highest SOC concentration was found in the S-air masses category.
Figure 6 shows the derived three trajectory clusters in the spring.The three clusters were classified according to directions as south of China (S), Northwest China (NW), and coastal areas in the east of China (E).Among the three identified trajectory clusters, NW took the dominant position, accounting for 62.5% of the total, while S and E happened less frequently, accounting for 18.75% and 18.75%, respectively.The summary of statistical analysis for carbonaceous concentrations of each transport cluster is listed in Table 6.Carbonaceous areole concentration sequences of the three clusters in descending order were E (OC: 20.22μg/m 3 , EC: 3.92 μg/m 3 ) > S (OC: 13.98 μg/m 3 , EC: 2.67 μg/m 3 ) > NW (OC: 7.77 μg/m 3 , EC: 2.28 μg/m 3 ).OC/EC ratio sequences of the three clusters in descending order were E (4.89) > S (4.39) > NW (3.77) (Table 3).The air masses originating from relatively clean northwest areas [8] were linked to lowest OC and EC concentrations, which were 7.77 and 2.28 μg/m 3 , respectively.
Since the chemical and optical properties of OC and EC were different, their influence on the atmosphere was different.Solar radiation can be scattered by OC and directly absorbed by EC.Meanwhile, following CO2, EC acted as the second most important component causing global warming [24].Effective carbon ratio (ECR, calculated as SOC/ (POC + EC)) was proposed by Safai, Raju [6], and it can be applied to assess the influence of carbonaceous aerosols on climate.Higher ECR value indicates lower EC and POC concentrations, which may result in a decreasing level of atmospheric warming effect.According to the study results, the ECR value of the N/NE-air masses (an average of 0.210) was much lower than that of the S-air masses (an average of 0.855) and similar to that of the E-air masses (an average of 0.289) in autumn.In spring, the ECR value of the S-air masses (an average of 0.579) was a little higher than that of the E-air masses (an average of 0.338) and NW-air masses (an average of 0.432) (Figures 8 and 9).As can be seen from Table 5, S occupied the dominant position, accounting for 43.75% of the total, while E-air masses and N/NE-air masses happened less frequently, accounting for 31.25% and 25%, respectively.Compared with E-air masses and S-air masses whose PM 10 concentrations were 70.52 µg/m 3 and 66.58 µg/m 3 , respectively, N/NE-air masses had a relatively higher PM 10 concentration of 92.33 µg/m 3 , due to the influence of dust storm events in this region.In addition, the sequence of OC concentrations among the three categories in descending order was S-air masses (8.01 µg/m 3 ) > N/NE-air masses (6.81 µg/m 3 ) > E-air masses (6.11 µg/m 3 ), and the sequence of EC concentrations in descending order was E-air masses (3.01 µg/m 3 ) > N/NE-air masses (2.70 µg/m 3 ) > S-air masses (1.99 µg/m 3 ).The fact beyond expectation is that S-air masses had the highest OC concentration, which was an average of 8.01 µg/m 3 .As they always came from the sea and were relatively clean, their EC concentration was the lowest.However, compared with the YRDR and northern China, the rapidly developing PRDR situated in the air mass pathway owns a different industrial structure, and the famous ozone and NO X pollution there could favor the formation of SOA [2,38], and the highest SOC concentration was found in the S-air masses category.Figure 6 shows the derived three trajectory clusters in the spring.The three clusters were classified according to directions as south of China (S), Northwest China (NW), and coastal areas in the east of China (E).Among the three identified trajectory clusters, NW took the dominant position, accounting for 62.5% of the total, while S and E happened less frequently, accounting for 18.75% and 18.75%, respectively.The summary of statistical analysis for carbonaceous concentrations of each transport cluster is listed in Table 6.Carbonaceous areole concentration sequences of the three clusters in descending order were E (OC: 20.22 µg/m 3 , EC: 3.92 µg/m 3 ) > S (OC: 13.98 µg/m 3 , EC: 2.67 µg/m 3 ) > NW (OC: 7.77 µg/m 3 , EC: 2.28 µg/m 3 ).OC/EC ratio sequences of the three clusters in descending order were E (4.89) > S (4.39) > NW (3.77) (Table 3).The air masses originating from relatively clean northwest areas [8] were linked to lowest OC and EC concentrations, which were 7.77 and 2.28 µg/m 3 , respectively.Since the chemical and optical properties of OC and EC were different, their influence on the atmosphere was different.Solar radiation can be scattered by OC and directly absorbed by EC.Meanwhile, following CO 2 , EC acted as the second most important component causing global warming [24].Effective carbon ratio (ECR, calculated as SOC/ (POC + EC)) was proposed by Safai, Raju [6], and it can be applied to assess the influence of carbonaceous aerosols on climate.Higher ECR value indicates lower EC and POC concentrations, which may result in a decreasing level of atmospheric warming effect.According to the study results, the ECR value of the N/NE-air masses (an average of 0.210) was much lower than that of the S-air masses (an average of 0.855) and similar to that of the E-air masses (an average of 0.289) in autumn.In spring, the ECR value of the S-air masses (an average of 0.579) was a little higher than that of the E-air masses (an average of 0.338) and NW-air masses (an average of 0.432) (Figures 8 and 9).

Conclusions
PM10 samples were collected at a high elevation mountain site during August-September, 2011 and March-May, 2012 in south China.The detected average concentrations of OC and EC were 6.89, 2.40 μg/m 3 and 10.58, 2.58 μg/m 3 in spring and autumn, respectively.SOC accounted for 31.0% of the total OC in autumn and 28.0% of the total OC in spring.The correlation between SOC and [H + ]strong

Conclusions
PM 10 samples were collected at a high elevation mountain site during August-September, 2011 and March-May, 2012 in south China.The detected average concentrations of OC and EC were 6.89, 2.40 µg/m 3 and 10.58, 2.58 µg/m 3 in spring and autumn, respectively.SOC accounted for 31.0% of the total OC in autumn and 28.0% of the total OC in spring.The correlation between SOC and [H + ] strong in PM 10 was not as strong as that in PM 2.5 , indicating that reactions catalyzed by heterogeneous acid may have contributed to SOA formation in fine particles.Results of PCA analysis suggested the carbonaceous aerosols at Mount Lu may have been contributed by multiple sources.During the study period, air masses that originated from southern China happened most frequently in autumn, and northwest China occurred most frequently in spring.The highest OC concentration and lowest EC concentration were found in the category of S during autumn and the lowest OC and EC concentration were related with the air mass from the NW cluster during spring.

Figure 1 .
Figure 1.Map showing the location of the sampling site at Mount Lu and nearby geographical settings.Figure 1. Map showing the location of the sampling site at Mount Lu and nearby geographical settings.

Figure 1 .
Figure 1.Map showing the location of the sampling site at Mount Lu and nearby geographical settings.Figure 1. Map showing the location of the sampling site at Mount Lu and nearby geographical settings.

Figure 4 .Figure 5 .
Figure 4. Scatter plot between OC and EC concentrations in autumn.

Figure 5 .
Figure 5. Scatter plot between OC and EC concentrations in spring.

Figure 6 .
Figure 6.Seventy-two hour backward trajectories for PM10 (particulate matter) samples at Mount Lu in autumn.

Figure 6 .
Figure 6.Seventy-two hour backward trajectories for PM 10 (particulate matter) samples at Mount Lu in autumn.

Figure 7 .
Figure 7. Seventy-two hour backward trajectories for PM10 samples at Mount Lu in spring.

Figure 7 .
Figure 7. Seventy-two hour backward trajectories for PM 10 samples at Mount Lu in spring.

Figure 7 .
Figure 7. Seventy-two hour backward trajectories for PM10 samples at Mount Lu in spring.

Figure 9 .
Figure 9. Effective carbon ratio (ECR) values for different air mass trajectories in spring.

Table 2 .
Comparisons of EC (elemental carbon) and OC (organic carbon) concentrations, and OC/EC ratios among various background sites around the world.

Table 2 .
Comparisons of EC (elemental carbon) and OC (organic carbon) concentrations, and OC/EC ratios among various background sites around the world.
Figure 2. Temporal variations of OC (organic carbon) and EC (elemental carbon) concentrations in autumn.Figure 3. Temporal variations of OC and EC concentrations in spring.

Table 2 .
Comparisons of EC (elemental carbon) and OC (organic carbon) concentrations, and OC/EC ratios among various background sites around the world.
Figure 2. Temporal variations of OC (organic carbon) and EC (elemental carbon) concentrations in autumn.Figure 3. Temporal variations of OC and EC concentrations in spring.

Table 3 .
PCA (principal component analysis) analysis of carbonaceous species for PM 10 (particulate matter) autumn samples.

Table 4 .
PCA (principal component analysis) analysis of carbonaceous species for PM 10 (particulate matter) spring samples.

Table 5 .
Occurrence percentage of different air mass trajectories, mean concentrations of PM10 (particulate matter), OC (organic carbon), EC (elemental carbon) and SOC (secondary organic carbon) for each trajectory at Mount Lu during autumn.

Table 6 .
Occurrence percentage of different air mass trajectories, mean concentrations of PM10, OC, EC and SOC for each trajectory at Mount Lu during spring.

Table 5 .
Occurrence percentage of different air mass trajectories, mean concentrations of PM 10 (particulate matter), OC (organic carbon), EC (elemental carbon) and SOC (secondary organic carbon) for each trajectory at Mount Lu during autumn.

Table 6 .
Occurrence percentage of different air mass trajectories, mean concentrations of PM 10 , OC, EC and SOC for each trajectory at Mount Lu during spring.

Table 5 .
Occurrence percentage of different air mass trajectories, mean concentrations of PM10 (particulate matter), OC (organic carbon), EC (elemental carbon) and SOC (secondary organic carbon) for each trajectory at Mount Lu during autumn.

Table 6 .
Occurrence percentage of different air mass trajectories, mean concentrations of PM10, OC, EC and SOC for each trajectory at Mount Lu during spring.