Regulatory effects on particulate pollution in the early hours of Chinese New Year, 2015
- 1.4k Downloads
Human activities are a key driver of air pollution, so it is hardly surprising that celebrations affect air quality. The use of fireworks contributes to high particulate concentrations in many parts of the world, with the Chinese Lunar New Year (spring festival) particularly noticeable, as firecrackers are traditionally used to drive off evil spirits. Fireworks lead to short-term peaks in the concentration of PM10, PM2.5 and SO2. Regulatory actions that restrict the use of fireworks have been evident in China since the 1990s. This paper investigates the particulate concentrations in nine Chinese cities (Beijing, Chengdu, Chongqing, Tianjin, Xi’an, Nanjing, Shanghai, Guangzhou and Shenzhen, along with Hong Kong (a Special Administrative Region) and Taipei and Kaohsiung (Taiwan) with a particular focus on the celebrations of 2015. Extremely high concentrations of particulate matter were observed, with some sites revealing peak PM10 concentrations in excess of 1000 μg m−3 in the early hours of the New Year. In Beijing, Tianjin and Chongqing, the activities caused high particulate matter concentrations at most sites throughout the city. These peaks in particulate load in the early hours of Chinese New Year do not appear to be closely related to meteorological parameters. However, in cities where fireworks appear to be better regulated, there are fewer sharp pollution peaks just after midnight, although lowered air quality can still be found in the outer parts of some cities, remote from regulatory pressures. A few cities seem to have been effective at reducing the impact of the celebrations on air quality, with Nanjing a recent example. An increasing focus on light displays and electric lanterns also seems to offer a sense of celebration with much reduced impacts on air quality.
KeywordsChina Fireworks Hong Kong PM2.5 PM10 Taiwan
Human activities are a key driver of air pollution so it is hardly surprising that celebrations and cultural activities can have a profound impact. One of the best studied is the regularly occurring weekend effect, which is defined as the difference of air pollutant concentrations between weekdays and weekends, with a general reduction of major pollutants. For instance, Qin et al. (2004) reported that the average concentrations of NOx, CO, NMOC and PM10 at weekends were lower than those on weekdays in southern California. It was first observed in the USA in the 1970s (Jimenez et al. 2005), and since then, many studies have reported these effects that are influenced by traffic rush hours (e.g., Cerro et al. 2014; Henschel et al. 2015), population size (e.g., Butenhoff et al. 2015) and degree of urbanisation (e.g., Huryn and Gough 2014). The phenomenon can also be seen in China; for example, both Tang et al. (2008) and Lei et al. (2015) reported lower concentrations of primary pollutants at weekends compared with those on weekdays in Shanghai and Beijing, respectively.
Holidays often mean that factories are close and people spend more time at home, leading to lower pollutant concentration, which has been termed the holiday effect. For example, the drastic decrease of primary pollutant emissions (83–98% of NO) during the Jewish Day of Atonement was reported by Levy (2013). Meanwhile, Tan et al. (2009) revealed lower concentrations of NOx, CO and non-methane hydrocarbons at Chinese New Year. As this is such a major holiday, it is hardly surprising that the holiday effect is widely observed. The concentrations of SO2 and PM10 in Taiwan from 1994 to 2006 were lower during Chinese New Year (or the Spring Festival, sometimes termed the Lantern Festival in Taiwan), while the concentration of ozone was higher (no titration by NO). In China, the Spring Festival led to a general improvement in air quality (e.g. Li et al. 2006; Tan et al. 2009; Gong et al. 2014; Lei et al. 2015; Zhao et al. 2015). However, this is not always true as research on the Spring Festival effect in 31 key Chinese cities found no significant reduction in the concentration of PM2.5 and PM10 during the holiday compared with the period that followed (Chen et al. 2014). In Shanghai, there can also be a Spring Festival rush hour as people prepare for the holiday (Huang et al. 2012), which not only enhances primary pollutant concentrations but also showed sharp peaks in particulate peaks during past New Year celebrations (Zhang et al. 2010).
A range of cultural activities can directly enhance primary pollutants, such as the Sunday roast of Victorian England (Brimblecombe 1987) or barbecues (Tsai et al. 2015). There are numerous reports on the impact of key events where fireworks contribute to visibility reduction (Singh et al. 2015), toxic metals (e.g., Camilleri and Vella 2010; Kong et al. 2015a), illicit use of the metalloid arsenic (Sterba et al. 2013) and enhanced particulate loads in: Spain (Moreno et al. 2010), Slovenia (Mlakar et al. 2012), the USA on Independence Day (Seidel and Birnbaum 2015) or German New Year (Drewnick et al. 2006), in India during the Diwali festival (Ravindra et al. 2003; Perrino et al. 2011; Chatterjee et al. 2013; Bhatnagar and Dadhich 2015) or the numerous festivals that occur throughout the summer in Malta (Camilleri and Vella 2010). Air pollution from fireworks is frequently observed at the Chinese Lunar New Year (Spring Festival) period; widely celebrated in Asia and within the Chinese diaspora. Firecrackers are thought to drive away evil spirits, that lurk around to torment human beings, but the noise causes them to vanish into thin air (Wong 1967); however, such celebrations contribute to a reduction in air quality. Tsai et al. (2012) found that the average concentration of PM10 rose to high levels over Kaohsiung Harbour, influenced by fireworks during Taiwan’s lantern festival. Gong et al. (2014) reported a reduction in aerosol during the Spring Festival and revealed that the concentrations of major air pollutants had significantly decreased around the holiday, but a short-term peak could be seen for PM10, NO2 and SO2, due to fireworks along with peaks in the concentration of a range of metals Sr, K, Ba, Pb, Al, Mg, and Cu, (Chang et al. 2011), dicarboxylic acids (Wang et al. 2007). There has been concern that even relatively short exposures to metallic elements from fireworks might have health implications (Yang et al. 2014). Additionally perchlorates associated with fireworks as an oxidant can have health effects along with the potential to cause broader ecological damage (Sijimol and Mohan 2014). The impact of New Year fireworks on air quality has been studied in a number of Chinese urban areas: Yanshui in Taiwan (Chang et al. 2011), Beijing (Wang et al. 2007), Jinan (Yang et al. 2014), Lanzhou (Zhao et al. 2014), Nanning (Yan 2011), Pearl River Delta (Zhao et al. 2015), Wuxi (Cao 2014) and Xian (Wang et al. 2008; Shen et al. 2009; Zhou et al. 2013).
Mainland China: Starting 18 February, ending 24 February.
Hong Kong: Starting 19 February, ending 21 February
Taiwan: Starting 18 February, ending 23 February.
Mainland China: Data for 11 monitoring stations in Beijing and Shenzhen, ten in Guangzhou and Shanghai, eight stations in Tianjin, seven stations in Chengdu, 12 stations in Chongqing, 13 stations in Xi’an and nine stations in Nanjing (http://aqicn.org/city/).
Hong Kong: Hong Kong Environmental Protection Department (HKEPD) data for 12 general stations and three roadside stations (http://epic.epd.gov.hk/EPICDI/air/station/?lang=en)
Taiwan: Taiwan Environmental Protection Administration (TEPA) data for seven monitoring stations in Taipei and 12 stations in Kaohsiung (http://taqm.epa.gov.tw/taqm/en/HourlyData.aspx).
Meteorological data was taken from Weather Underground: https://www.wunderground.com/history/ sites in some cities needed to be stratified into various administrative areas, and although these are somewhat arbitrary, this has been done as follows: (i) Beijing; the inner city was defined as urban area i.e. inside the 2nd Ring Road, with suburban being the area between 2nd and 5th Ring Road. Outskirts are beyond 5th Ring Road, with rural the furthest sites or outer suburbs (https://en.wikipedia.org/wiki/Beijing). (ii) Tianjin; the Heping District is defined as urban while the peripheral administrative divisions a denoted as suburban (https://en.wikipedia.org/wiki/Tianjin). (iii) Shenzhen; Luohu, Futian and NanShan are defined as urban areas. Guangming and Dapeng are the new districts and remote, so classified as rural areas, with other districts are defined as suburban (see: https://en.wikipedia.org/wiki/Shenzhen).
The correlation between particulate concentrations and meteorological variables was determined using Wessa Free Statistics Software (https://www.wessa.net/), which was convenient as it gave Kendall τ and Spearman r s in addition to the parametric Pearson r. The short data sets from individual sites in cities were compared using the Wilcoxon signed-ranks test. This was used most typically to compare concentrations measured during the celebrations [00:00–02:00] with those before and afterwards ([22:00–24:00] and [02:00–04:00]). This test was adopted as an alternative to the paired t test when assessing the difference between measurements from the monitoring stations across given cities, because the concentrations seemed skewed. The results of this signed-rank test are reported with the significance as a two-tailed p value, the test statistic W and the number of pairs n (i.e. sites). As the number of sites in the cities was small (i.e. 7–13), the observed value of W must be referred to an exact sampling distribution (Mosteller et al. 1973). In this work we used the on-line calculators available at the VassarStats Website for Statistical Computation (http://www.vassarstats.net/).
In addition to showing the position of the cities considered in this study, Fig. 1 also gives an indication of the overall weather conditions. It suggests a colder north, with a high-pressure area that probably led to stable conditions and the chance to build up pollutants. In the north of China, high pollutant concentrations can result from the large amounts of fuel required for heating. In the warmer south dispersion along the coast means, air pollution tends to be lower in the winter season. The annual particulate concentrations in Beijing, Tianjin, Xi’an are typically the highest. The cities of the coastal south are usually lower, along with Hong Kong and Taiwan. Measurements of temperature, wind speed and relative humidity from each of the cities are shown in the small graphs that surround the meteorological chart. Much as would be expected, these do not suggest sharp changes with the transition to the New Year.
Figure 2b, c show the hourly particulate concentrations averaged across Beijing for the days around Chinese New Year for both 2015 (black line) and 2014 (grey line). The temporal changes in Beijing over these longer periods before and after the Chinese New Year reveal no further obvious sharp peaks. However, a dust storm occurred in late February 2015 (RV 2015) and is evident 3 days after New Year, when a broad area of dust crossed Beijing driven by a northwest airflow in Mongolia. This led to more than 10 h of high PM10 concentrations, which peaked around 714 μg m−3 (Cheng et al. 2015).
The graph of the relationship between the PM2.5 against PM10 is the only one in Fig. 3 that is particularly convincing; all the others being rather scattered. Each dot in the plots represents a city. The correlation matrix in the lower left of Fig. 3 suggests that there is a significant relationship between PM2.5 against PM10 (r = 0.981 and p = 0.00). This is also true for correlation between the directly observed PM2.5 and PM10. (not shown but r = 0.961 and p = 0.00). There is a slight though weaker negative correlation between added PM2.5 and PM10 and temperature (PM2.5: r = −0.557, p = 0.06 and PM10: r = −0.540 p = 0.07). This seems likely to arise because pollution from fireworks is rather high in the two colder northern cities (Beijing and Tianjin), which have high peaks in particulate concentrations in the early hours of Chinese New Year. Not surprisingly, wind speeds also seem negatively correlated with peaks in PM2.5 against PM10 (shown in Fig. 3) and measured particulate matter concentrations (not shown); albeit none are statistically significant. Population shows a slight positive correlation with particulate matter, but not at significance levels (> 90%). The generally low level of significance apparent from the correlation matrix leaves us with an impression that the New Year peaks in particulate concentrations are not predominantly driven by meteorological conditions. This adds to the evidence presented in Fig. 1, which suggests no sharp changes in meteorological conditions at the beginning of the New Year.
Cities across China have adopted rather different regulations with respect to the use of fireworks at New Year. As noted by Li et al. (2006), who investigated air pollution in Beijing during the spring festival over the period 2000~2006, the intense use of fireworks over a short time created a serious air pollution problem. There had been attempts at controlling the problem since the 1990s, but from 2006, Beijing initiated a policy that that allowed people to celebrate with fireworks, but restricting use from Chinese New Year’s Eve to 24:00 the following day for locations within the 5th Ring Road. There was evidence of high pollutant concentrations across the city, although this improved with the adoption of regulations (Li et al. 2006). Despite the attempt to alleviate high pollution levels through time restrictions on the use of fireworks (Appendix Table 1), there is still much evidence of large concentrations of air pollutants, most notably particulate matter and sulphur dioxide across Beijing (as shown in Fig. 2).
The profile of changing PM10 concentrations at individual stations in Beijing for New Year’s Eve and the early morning of the New Year is shown in Fig. 6a. It is clear that there is a widespread increase in the concentration of particulate matter across the city in the early morning and a high significance revealed by the Wilcoxon test (p = 0.0036, as tabulated in Fig. 6a). As noted earlier, the changes are largest at stations remote from the city centre. Examining individual station records suggests that Huairouzhen which lies beyond the 6th Ring Road has concentrations that appear to exceed 1000 μg m−3. Concentrations are also high, in excess of 500 μg m−3, in two other locations: (i) Wanshouxigong in the Baizhifang Residential District in the southwest just inside the 2nd Ring Road and (ii) Shunyixincheng in the Shunyi District northeast of Beijing’s Capital International Airport. Thus, the very highest concentrations are often away from the centre of the city; early morning peaks are observed at all sites around the city. Here, concentrations seem to be some 250 μg m−3 above what might be expected where there were no contributions from fireworks in the concentrations measured in the early hours of the New Year (see the trend lines of Fig. 6a). The attempt to regulate the times permissible for fireworks seems ineffective in keeping particulate concentrations low. However, Beijing has started to include public displays at around midnight on New Year’s Eve. High air concentrations during the celebrations of 2017 drew considerable comment, which may increase enthusiasm for such public displays.
Chongqing (Fig. 6b) and Tianjin (Fig. 6c) have somewhat similar policies to Beijing, restricting the time over which fireworks are permitted in the central parts of the city (see Appendix Table 1). All sites show very pronounced peaks in PM10 concentrations in the early morning in Tianjin. Xi’an (Fig. 6d) has no fireworks ban for Chinese New Year although typically fireworks should not be used. As seen in Fig. 5, measurements from of Xi’an show more variable profiles in PM10 concentrations through the night, which may explain the low statistical significance of these changes. Nevertheless, a peak in the PM10 concentrations is evident in the early morning for a number of sites, but the concentrations are not especially high when compared to Beijing, Chongqing and Tianjin, but Xi’an is a smaller city. The changes in Shanghai (Fig. 6e) are rather small, with peaks suggesting the addition of only 50–100 μg m−3 to early morning concentrations of PM10, nevertheless, the early morning increase across the city is significant (p = 0.005).
The cities of Chengdu and Shenzhen have bans in certain regions (Appendix Table 1). Chengdu (Fig. 6f) shows little evidence of a sharp morning peak in particulate concentrations suggesting some success with their regulation of pollution from fireworks. There was a general increase in pollution in this city on New Year’s Day (p = 0.02), but the early morning changes are small, on average only 15 μg m−3. Figure 6f makes a less convincing case for a firework source in Chengdu compared with cities such as Beijing. In Shenzhen (Fig. 6g), it seems that long standing regulations are fairly effective suggesting little increase in PM10 concentrations, although in the city, overall the peak in the early morning hours is significant (p = 0.0012). However, this arises from clear peaks in particulate concentrations (Fig. 6g) associated with measurements made in: Kuiyong, Nanyou, Nan’au and perhaps less clearly Xixiang. These sites are all rather distant from the city centre, where controls are in force. Once these remote sites are removed, the significance of Shenzhen’s early morning increase in PM10 declines (i.e. p > 0.05). With the exception of these remote sites, the impact of fireworks in Shenzhen appears relatively small compared with changes seen in Beijing and Tianjin. The main city of Guangdong Province, Guangzhou has permitted fireworks in suburban areas, although it has banned their use in central urban areas since 1992. Here, results suggest little clear contribution from fireworks, with early morning values or PM10 being somewhat lower than other times (as shown by the negative W statistic in Fig. 6g). Nanjing introduced strict controls in 2015 and shows no evidence of a firework contribution to particulate matter (Fig. 6i) and a significantly negative W statistic.
Outside the Chinese Mainland, Hong Kong (Fig. 6j) and the cities of Taiwan: Taipei (Fig. 6k) and Kaohsiung (Fig. 6l), seem to reveal little evidence of pollutants from fireworks. They perhaps hint at an effective reduction of emissions. In Taiwan fireworks are allowed, although not necessarily used to a great extent or especially popular. There may be some increases in early morning PM10 in Taipei and Kaohsiung (p = 0.05, p = 0.04), but they remain small (Fig. 6k, l). Temple parades may still use them although these are not primarily New Year’s Eve activities. The use of fireworks is spread throughout the year, with just a few temples celebrating a midnight event at the New Year (e.g. the God of War Temple in Yanshui, Tainan City). A particular focus in Taiwan has been the creation of a less polluting lantern festival, which is popular with tourists. The lanterns are often electrical, thus reducing the potential for air pollution (see TB 2016).
Across a city, there may be variations because of local regulations, as seen in Shenzhen (Fig. 6g), but significant spatial variation can be seen in some cities such as Xi’an (Figs. 5 and 6d). Here, some sites show peaks after midnight, some show peaks at other times during the evening, while others show little change.
Interest in restricting the use of fireworks in China spans more than two decades. This confronts some long-held cultural beliefs and deeply embedded traditions. Li et al. (2006) believed that regulations played an important role in reducing PM10 in areas of Beijing where fireworks were forbidden. Nevertheless, Wang et al. (2008) found a trend of increasing PM10 concentrations through New Year’s Eve in Xi’an in both urban and suburban areas, so concluded that the government should put forward a policy to ban fireworks. There has been a fairly restrictive ban on fireworks in the main areas of cities of the Pearl River Delta (Guangzhou and Shenzhen) since the early 1990s (Zhao et al. 2015). However, it has been argued that an increasing amount of PM2.5 on New Year’s Eve can still be observed in suburban areas in these two cities.
Overall our results suggest that while in some cities the celebration of New Year brings a noticeable decline in air quality, but a number of other cities seem to have made satisfying achievements in reducing the extent of the problem. The effectiveness of regulation might be expected in Hong Kong and Taiwan, given their different approaches to governance. Nevertheless, some cities on the Mainland: Chengdu, Shenzhen and Guangzhou, and most recently Nanjing seem to have relatively good air quality during the festivities. While a Nian culture still survives, it appears that regulation may be possible.
The evidence of distinctive peaks in air pollution from fireworks across individual cities can be variable, with the largest effects found at the outskirts, perhaps suggesting that regulations may be more relaxed at the margins. In cities where regulations are enforced, the evidence of fireworks activity in the PM10 concentrations seems to occur well away from the centre, such as in the more remote parts of Shenzhen, again evidence of lower concern well away from urban centres. Such locations might well benefit from considering the work of Mlakar et al. (2012) from Slovenia who make an argument for selecting areas for fireworks displays according to knowledge about air pollution dispersion. Although the focus here is on China, it suggests the relevance of regulation for other parts of the world where fireworks are used at specific times such as US Independence Day, Hindu Diwali (Perrino et al. 2011; Chatterjee et al. 2013) and Guy Fawkes celebrations of England and some Commonwealth countries (Singh et al. 2015). The example from China may be less relevant to other places, such as Malta, where more than 80 individual villages will use fireworks for local festivals, often on different days (Camilleri and Vella 2010).
The celebration of Chinese New Year is associated with loud noises, firecrackers, coloured lanterns and, in many cases, air pollution. The cities of Beijing, Chongqing, Tianjin and Shanghai, where fireworks are allowed albeit with time restrictions, show significant (p < 0.05) peaks in the early hours of the New Year and substantial increases in PM10 concentrations (> 25 μg m−3). Pollution, waste and safety issues have seen regulatory pressures to restrict the use of fireworks and change behaviour for a number of years. Nanjing is particularly notable for its high air quality during the 2015 New Year, much improved over earlier years. To some extent, regulations have been more successful at reducing an obvious peak in particulate concentrations in the south of China. It may be because traditions are different, or that traditions have changed. The differences may also reflect provincial differences in regulatory procedures that could come apparent in a large country.
The desire to have celebrations that have a lower impact on air quality may well be achieved without entirely removing the celebratory nature of this important event in the Chinese calendar. Taiwan has been notable in promoting the event as more about lanterns than fireworks. Hong Kong has been consistent in adopting carefully controlled public displays of fireworks and to restrict private use. They also to ensure that those used are sourced to minimise pollution, not only in the air but also the deposition of toxic materials to the environment. The Environmental Protection Department analysis argues that “the National Day Fireworks Display and the New Year’s Eve Pyrotechnic Show… last for a short duration involving high-altitude fireworks discharge above the sea.... This accounted for 0.1 per cent of Hong Kong's total emission of RSP in 2011” (HKSAR 2013). In the past, firework displays were more frequent over Hong Kong’s Victoria Harbour. Now there is a celebration of the city each evening with a stunningly orchestrated display of lights on the major tall buildings of Hong Kong Island combined with beams from moveable searchlights and lasers. Thus, there is almost no potential for enhanced particulate emissions. Environmental regulation routinely limits the freedom of choices available to individuals, but the celebration of Chinese New Year may still be widely enjoyed even when restrictions on the use of fireworks are enforced.
In a paper with such wide ranging cultural considerations, we needed advice from a number of people who were most willing to share their thoughts, particularly: Winnie Lo on Hong Kong, Joseph Lee on Taiwan and Katie Chang on celebrations in Xi’an. Nicky Lam, Keith Ngan and Wen Zhou provided meteorological insight. The work here received support from the City University of Hong Kong (Project No. 9380071) and benefitted from the NERC grant to the University of East Anglia INHANCE APHH China programme (No. NE/N00714X/1).
- Bhatnagar, S., & Dadhich, S. (2015). Measurement of airborne particulate matter concentration levels in the ambient atmosphere. Journal of Energy Research and Environmental Technology, 2, 12–13.Google Scholar
- Brimblecombe, P. (1987). The big smoke. London: Routledge.Google Scholar
- Cao, L. (2014). The study on the impacts of setting off firecrackers to air quality during the spring festival in Wuxi city (Chinese). Pollution Control Technology, 27(3), 5–9.Google Scholar
- Chao, Y., Chen, R., & Young, C. (2014). Nian: when Chinese mythology affects air pollution. The Lancet, 383(9935), 2125.Google Scholar
- Chatterjee, A., Sarkar, C., Adak, A., Mukherjee, U., Ghosh, S. K., & Raha, S. (2013). Ambient air quality during Diwali Festival over Kolkata—a mega-city in India. Aerosol and Air Quality Research, 13, 1133–1144.Google Scholar
- Chen, X., Liu, Z., & Wu, P. L. (2014). Analysis on Chinese urban air quality “spring festival effect”: Evidence from 31 key cities in China (Chinese). Statistics & Information Forum., 29, 57–62.Google Scholar
- Cheng, N. L., Chen, T., Zhang, D. W., Li, Y. T., Sun, F., Wei, Q., Liu, J. L., Liu, B. X., & Sun, R. W. (2015). Air quality characteristics in Beijing during spring festival in 2015 (Chinese). Environmental Sciences, 36, 3150–3158.Google Scholar
- Henschel, S., Tertre, A. L., Atkinson, R. W., Querol, X., Pandolfi, M., Zeka, A., Haluza, D., Analitis, A., Katsouyanni, K., Bouland, C., Pascal, M., Medina, S., & Goodman, P. G. (2015). Trends of nitrogen oxides in ambient air in nine European cities between 1999 and 2010. Atmospheric Environment, 117, 234–241.CrossRefGoogle Scholar
- HKSAR (2013). Impacts of fireworks on air quality The Government of the Hong Kong Special Administrative Region. http://www.info.gov.hk/gia/general/201302/20/P201302200272.htm. Accessed 18 Aug 2017.
- Huang, K., Zhuang, G., Lin, Y., Wang, Q., Fu, J. S., Zhang, R., Li, J., & Deng, F.,. Q. (2012). Impact of anthropogenic emission on air quality over a megacity -revealed from an intensive atmospheric campaign during the Chinese Spring Festival. Atmospheric Chemistry and Physics, 12, 11631–11645.CrossRefGoogle Scholar
- Kong, S. F., Li, L., Li, X. X., Yin, Y., Chen, K., Liu, D. T., Yuan, L., Zhang, Y. J., Shan, Y. P., & Ji, Y. Q. (2015a). The impacts of firework burning at the Chinese Spring Festival on air quality: insights of tracers, source evolution and aging processes. Atmospheric Chemistry and Physics, 15(4), 2167–2184.CrossRefGoogle Scholar
- Kong, S., Li, X., Li, L., Yin, Y., Chen, K., Yuan, L., Zhang, Y., Shan, Y., & Ji, Y. (2015b). Variation of polycyclic aromatic hydrocarbons in atmospheric PM2.5 during winter haze period around 2014 at Nanjing: Insights of source changes, air mass direction and firework particle injection. Science of the Total Environment, 520, 59–72.CrossRefGoogle Scholar
- Lei, Y., Zhang, X. L., Tang, Y. X., Fan, G. Z., & Zhou, D. W. (2015). Holiday effects on PM2.5 and other major pollutants in Beijing (Chinese). Acta Scientiae Circumstantiae, 35(5), 1520–1528.Google Scholar
- Li, L. J., Li, J. X., Xin, L. Z., Li, H. J., & Wei, Q. (2006). Analysis of atmospheric air pollution of Beijing City in Spring Festival period (Chinese). China Environmental Science, 26(5), 537–541.Google Scholar
- Moreno, T., Querol, X., Alastuey, A., Amato, F., Pey, J., Pandolfi, M., Kuenzli, N., Bouso, L., Rivera, M., & Gibbons, W. (2010). Effect of fireworks events on urban background trace metal aerosol concentrations: is the cocktail worth the show? Journal of Hazardous Materials, 183, 945–949.CrossRefGoogle Scholar
- Mosteller, F., Robert, E. K., & Rourke, R. E. K. (1973). Sturdy statistics: nonparametrics and order statistics. Reading: Addison-Wesley Educational Publishers Inc.Google Scholar
- NJHB (2015). Why appeal to limit the use of firecrackers (in Chinese). http://www.njhb.gov.cn/43188/jfyhbz/jfdt/201502/t20150210_3194637.html. Accessed 18 Aug 2017.
- RV (2015). Yellow dust from China blows into South Korea, Reuters Video February 23, 2015. http://www.reuters.com/video/2015/02/23/yellow-dust-from-china-blows-into-south?videoId=363275101. Accessed 18 Aug 2017.
- SYCCA (2011). Statistical yearbook of China’s Civil Administration (中国民政统计年鉴) (in Chinese), China Statistical Press, Beijing.Google Scholar
- TB (2016). Taiwan Lantern Festival Heart of Asia, Tourism Bureau, Republic of China (Taiwan) https://www.eventaiwan.tw/cal_en/cal_19955. Accessed 18 Aug 2017.
- Wang, F. Q., Cai, X. L., & Zhou, A. S. (2008). Effect of firecracker setting-off on the PM10 and SO2 and NO2 in Xian (Chinese). Journal of Safety and Environment, 8(1), 82–86.Google Scholar
- Wong, C. S. 1967. A cycle of Chinese festivities. Singapore: Malaysia Publishing House Singapore.Google Scholar
- XEN (2011). Xi'an Evening News (西安晚报) 25 May 2011 (in Chinese), p. 3.Google Scholar
- Yan, M. (2011). Effect of firecrackers during spring festival on air in Nanning City (Chinese). Sichuan Environment., 30(6), 53–56.Google Scholar
- Yang, L., Gao, X., Wang, X., Nie, W., Wang, J., Gao, R., Xu, P., Shou, Y., Zhang, Q., & Wang, W. (2014). Impacts of firecracker burning on aerosol chemical characteristics and human health risk levels during the Chinese New Year celebration in Jinan, China. Science of the Total Environment, 476, 57–64.CrossRefGoogle Scholar
- Ye, C., Chen, R., & Chen, M. (2016). The impacts of Chinese Nian culture on air pollution. Journal of Cleaner Production 112, 1740–1745.Google Scholar
- Zhao, W., Fan, S., Xie, W. Z., & Sun, J. R. (2015). Influence of burning fireworks on air quality during the Spring Festival in the Pearl River Delta (Chinese). Environmental Sciences, 36(12), 4358–4365.Google Scholar
- Zhou, B.-H., Zhang, C.-Z., & Wang, G.-H. (2013). Study on pollution characteristics of carbonaceous aerosols in Xi'an city during the spring festival. Huanjing Kexue/Environmental Science, 34(2), 448–454.Google Scholar
Open Access This article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.