Zita Ferenczi This email address is being protected from spambots. You need JavaScript enabled to view it.1, Kornélia Imre2,3, Mónika Lakatos1, Ágnes Molnár2,3, László Bozó1, Emese Homolya1, András Gelencsér2,3 

1 Hungarian Meteorological Service, Kitaibel 1, H-1024 Budapest, Hungary
2 ELKH-PE Air Chemistry Research Group, Egyetem 10, H-8200 Veszprém, Hungary
3 Research Centre for Biochemical, Environmental and Chemical Engineering, University of Pannonia, Egyetem 10, H-8200 Veszprém, Hungary

Received: March 5, 2021
Revised: June 16, 2021
Accepted: June 17, 2021

 Copyright The Author(s). This is an open access article distributed under the terms of the Creative Commons Attribution License (CC BY 4.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are cited.

Download Citation: ||https://doi.org/10.4209/aaqr.210048  

  • Download: PDF

Cite this article:

Ferenczi, Z., Imre, K., Lakatos, M., Molnár, Á., Bozó, L., Homolya, E., Gelencsér, A. (2021). Long-term Characterization of Urban PM10 in Hungary. Aerosol Air Qual. Res. 21, 210048. https://doi.org/10.4209/aaqr.210048


  • Marked seasonality in PM10 concentration observed in Hungary.
  • Variations in PM10 levels were decomposed to principal components of pollution.
  • PM10 have association with temperature, wind speed and boundary layer height.
  • Regression model for predicting daily PM10 concentration was developed.


Over urban areas in Hungary, the annual average PM10 concentrations are not frequently higher than 40 µg m–3. Despite the mitigation efforts of the local governments, the annual number of exceedances of the daily limit of 50 µg m–3 is higher than what is outlined in EU Directive No 2008/50/EC. The goal of the present study is to assess the characteristics of the temporal (annual, seasonal, daily) variations in PM10 concentrations in selected Hungarian cities with large populations, where most of the exceedances have been reported. The impacts of meteorological conditions on the measured PM10 concentrations and their temporal variations are also evaluated. An important aspect of studying the trends of air pollution is that the tendencies depend not only on the emissions of certain pollutants but also on the meteorological conditions in the area of interest. To analyse emission-related trends, the meteorological signal must be removed from the data series. In this study, the Kolmogorov-Zurbenko (KZ) filter was used for this type of trend separation. Moreover, multiple nonlinear regression analysis was used to find relationships between the PM10 concentration and several meteorological parameters. The goal of this analysis is to estimate the expected daily mean PM10 concentration values. The results of this analysis demonstrate that the regression equation can provide an adequate method for PM pollution forecasting. In addition to the hourly PM10 concentrations and basic meteorological data, global radiation and boundary layer height were considered in the characterization process.

Keywords: PM10, Cold season episode, Regression analysis, Kolmogorov-Zurbenko (KZ) filter


Currently, particulate matter (PM) is one of the most critical atmospheric pollutants since it has negative impacts not only on human health but also on environmental issues such as visibility, infrastructure, and ecosystems (Horvath, 1995; Lim et al., 2012; Fang et al., 2013; Kuzmichev and Loboyko, 2016; Tidblad et al., 2017; De Marco et al., 2019).

The primary sources of the particles are highly variable in intensity, space and time, and emitted particles of different sizes and compositions have widely different fates and effects depending on atmospheric conditions. In addition, aerosols can be formed in the atmosphere (secondary aerosols), adding to the immense complexity of the PM issue. It is therefore a challenge to reduce PM emissions (EU Directive, 2016) and the associated risks to human health from exposure to PM. A better understanding of the status of and trends in air quality in Europe is crucial to support European, national, and regional governments in policy-making and implementation, as well as to improve the tools of air quality assessment and management (Guerreiro et al., 2014).

PM is a complex mixture of solid- or liquid-phase primary and secondary particles. Their physical and chemical properties, such as shape, size, solubility, residence time, toxicity, and chemical composition and structure, vary greatly. Among them, the chemical composition and particle size are key factors in understanding the behaviour and role of the particles in atmospheric processes. These characteristics impact human health; they control aerosol optical properties and hygroscopicity, playing a substantial role in the atmospheric radiation budget and cloud formation (Seinfeld and Pandis, 2012). Local and regional meteorological factors, including wind speed, wind direction, vertical atmospheric stability, long-range transport, and pollution dispersion, play an important role in determining PM concentrations. For this reason, the analysis of local and regional meteorology is important to better understand the processes that are responsible for the spatial and temporal distribution of PM (Demuzere et al., 2009; Velders and Matthijsen, 2009; Pearce et al., 2011; Barmpadimos, et al., 2012; Chen et al., 2018).

In Europe, the emissions of many primary air pollutants have decreased substantially over the past decades, resulting in improved air quality across the region (European Environment Agency, 2019). Nevertheless, several emission sources remain for which much less progress has been achieved. Examples are biomass burning and residential heating or emissions from agricultural activities, all of which are significant primary sources of particulate matter in Hungary. Non-industrial sources account for more than 50% of total emissions, mostly from residential heating (Kis-Kovács et al., 2019). Resuspended particles from agricultural operations, bare soils, or road traffic are also considered uncontrolled and significant sources. The time series of total emissions by sector (GNFR – gridded nomenclature for reporting) in Hungary between 2007 and 2017 does not show a definitive trend.

In urban areas, residential combustion and traffic-related emissions (exhaust and non-exhaust) are the main primary sources of PM. Particulate matter from roads (resuspended by wind or other anthropogenic activities) significantly contributes to urban PM10, e.g., up to 30% in Veszprém, Hungary (Jancsek-Turóczi et al., 2013). Residential wood combustion is the largest single source of organic aerosols. The aerosol emissions from this source are still significantly underestimated in Europe (van der Gon et al., 2015). According to Karagulian et al. (2015), in Central and Eastern Europe, domestic fuel burning (wood, coal and gas) might contribute up to 45% of PM10 emissions (while globally, its share can reach 15%).

PM is a complex mixture of solid- or liquid-phase primary and secondary particles. Their physical and chemical properties, such as shape, size, solubility, residence time, toxicity, and chemical composition and structure, vary greatly. Among them, the chemical composition and particle size are key factors in understanding the behaviour and role of the particles in atmospheric processes. These characteristics impact human health; they control aerosol optical properties and hygroscopicity, playing a substantial role in the atmospheric radiation budget and cloud formation (Seinfeld and Pandis, 2012). Local and regional meteorological factors, including wind speed, wind direction, vertical atmospheric stability, long-range transport, and pollution dispersion, play an important role in determining PM concentrations. For this reason, the analysis of local and regional meteorology is important to better understand the processes that are responsible for the spatial and temporal distribution of PM (Demuzere et al., 2009; Velders and Matthijsen, 2009; Pearce et al., 2011; Barmpadimos et al., 2012; Chen et al., 2018).

According to Barmpadimos et al. (2011), in Switzerland, PM10 concentrations are affected by wind gusts, temperature, the precipitation rate and the boundary layer depth. Dunea et al. (2015) reported that there were negative correlations between PM10 and temperature and solar radiation, while relative humidity and atmospheric pressure were positively correlated with PM10. Vardoulakis and Kassomenos (2008) found a significant correlation between PM10 and solar radiation during cold seasons, and these correlations became weaker during warm seasons. Most of these papers finally concluded that in addition to changes in anthropogenic emissions, changes in meteorology can be responsible for long-term changes in PM10 concentrations.

In Hungary, three important factors have essential effects on PM10 concentrations: local anthropogenic emissions, long-range transport (sources outside of the country) and meteorological conditions. It has been estimated that the background annual average PM10 mass concentration for continental Europe is 7.0 ± 4.1 µg m–3 (Van Dingenen et al., 2004), and the natural contribution to PM can range from 5% to 50% in different European countries. The effects of natural sources on PM10 concentrations are almost negligible in Hungary (Diapouli et al., 2017). The most important local emissions that have significant effects on the PM2.5 concentrations at an urban background site are traffic (19%) and biomass burning (24%) (Perrone et al., 2018), while the impacts of sources originating from the transboundary and countryside are significant, more than 30% (Thunis et al., 2017). The impact of traffic on PM10 is continuous throughout the year; however, the effect of residential heating is considerable only in winter; otherwise, it can be neglected. During spring and fall, depending on the local weather conditions, inhabitants use combustion equipment mostly at night. In winter, the effect of residential heating must be taken into account throughout the day.

In our previous work (Ferenczi and Bozó, 2017), the effect of transboundary sources on the air quality of the greater Budapest area was evaluated. We found that the contribution of long-range (transnational) atmospheric transport to the annual cumulative PM10 concentrations in Hungary was remarkably high (higher than 50%). However, during the winter, late fall and early spring, episodes of very poor air quality (exceedances of PM10 limit concentrations) were always caused by local (regional) emission sources in combination with special and highly unfavourable meteorological conditions—such as extensive cold air cushions—which prevent mixing and dilution of air pollutants. Usually, this type of meteorological condition is frequently associated with low ambient air temperatures, which further increases the use of solid fuels (wood and coal) and leads to an increase in PM10 emissions from domestic heating (Tarrason et al., 2018; Ferenczi et al., 2020). These synoptic conditions favour smog formation, and the effect of long-range transport is negligible compared to the role of local sources and processes. These events are usually terminated by markedly changing meteorological conditions (intensive horizontal and vertical mixing of the air), which restore the importance of long-range transport in determining PM10 concentrations.

The main objectives of the present work are to determine the spatial and temporal variability of the PM10 concentration in Hungarian cities, to separate the effects of emission sources and meteorology on PM10 concentrations, and finally to investigate the relationships between the PM10 level and meteorological parameters to identify the most important parameters that can be used in PM10 prediction.


2.1. Monitoring Sites

Three monitoring stations with significantly different characteristics (population, type of station) were selected for the detailed analysis of three cities, Budapest, Miskolc and Pécs. In these cities, exceedances of PM10 limit concentrations have been reported most often (Fig. 1). The data availability of hourly PM10 concentrations is sufficiently high at all three stations for statistical trend analysis.

Fig. 1. Number of exceedances of the threshold value (50 µg m–3) for the number of daily averages as a function of the season (green-spring, orange-summer, yellow-fal, blue-winter) (2007–2017). Dotted line indicates the limit value (35 days).Fig. 1. Number of exceedances of the threshold value (50 µg m–3) for the number of daily averages as a function of the season (green-spring, orange-summer, yellow-fal, blue-winter) (2007–2017). Dotted line indicates the limit value (35 days).

At several locations in Budapest (525.1 km2, 1,752,286 inhabitants), the monitoring of PM10 with fine temporal resolution started in 2007. The air quality monitoring network of Budapest consists of 12 stations that are classified as traffic (4), industrial (3) or background (5). Among the monitoring sites, the Gilice tér urban background station (located in the SE part of Budapest) was selected for our analysis, which is a standard meteorological and air quality monitoring station providing PM10 concentrations and detailed meteorological observations with good data coverage. This location is in the area of the Marczell György Main Observatory of the Hungarian Meteorological Service. The classification of this air quality monitoring site is suburban with a significant influence from major sources from the greater Budapest area.

Miskolc (236.7 km2, 159,000 inhabitants) is represented by the Búza tér station. The air quality monitoring network of Miskolc consists of 3 stations that are categorised as traffic (1) and background (2). The classification of the site is urban traffic with a significant contribution from traffic-related sources. Moreover, the whole city is located in an unfavourable geographical location in the valley of the Sajó River surrounded by the Bükk Mountains. Its special orography contributes to the development of long-lasting (several days up to weeks) and severe air pollution episodes.

In Pécs (162.8 km2, 148,000 inhabitants), the selected station (Boszorkány utca) is located in a suburban environment. The air quality monitoring network of Pécs consists of 3 stations that are classified as traffic (1) and background (2). The hourly PM10 data for our complex analysis have been available since 2009. One of the major industrial emission sources in this area is a coal-fuelled power plant equipped with two modern electrostatic precipitators. This development further decreases the PM10 emissions in the city. However, compared to Miskolc, the city of Pécs has more favourable orography: the northern part of the city is bordered by the Mecsek Mountains, but the southern side is open and flat.

2.2. Monitoring Methods

The evaluation of the air quality in Budapest, Miskolc, and Pécs is based on data from the Air Quality Monitoring Network of Hungary and meteorological observations from the Hungarian Meteorological Service. Calibration procedures and measurements of standards are used for air data quality control. The instruments and measurement methods fulfil the requirements of the pending EU standards. The concentration of PM10 was measured with different types of monitors based on the β-attenuation method. The flow rate of the PM analysers was calibrated twice a year, and the mass measurement was calibrated once a year.

To obtain reliable PM10 data, regular systematic quality assurance and quality control, standardized operating procedures and intercomparison measurements were performed. The PM10 data used in this study were collected and managed (validated) by the Hungarian Meteorological Service, Air Quality Reference Centre.

2.3. Data Analysis

All monitoring data were subdivided into four periods, spring (1 March–31 May), summer (1 June–31 August), fall (1 September–30 November) and winter (1 December–28 February), to account for the seasonal factors influencing particulate levels. The 1-hour data (PM10 concentrations and meteorological parameters) were averaged over 24-hour periods when at least 75% of 1-hour data were available for each time period. The averaged diurnal variations in PM10 concentrations at the monitoring stations were determined to build diurnal profiles of PM10 emissions factors used in chemical transport models in the future (Menut et al., 2012).

Initially, temporal variation analysis was carried out, then the Kolmogorov-Zurbenko (KZ) filter was used to spectrally decompose the pollutant time series, and finally, multiple regression analysis was performed to find the relationships between PM10 concentrations and several meteorological parameters. In the temporal variation analysis, 1-hour and, in other cases, 24-hour data were used. The KZ filter is suitable for separating both long- and short-term variations in time series. There are many similar filtering techniques, such as the anomaly technique and the wavelet transform, which can be used to separate the short-, seasonal- and long-term components of air quality data. However, the KZ filter has several advantages: it can be applied to a time series even if it includes missing data, it is an established method that has been widely applied, and it is relatively simple to use.

Finally a multiple nonlinear regression analysis was carried out to find relationships between the PM10 concentration and several meteorological parameters. This technique has been widely used for PM10 forecasting especially in urban areas. The statistically significant variables were selected for the PM10 prediction model.


3.1. Temporal Variation in the PM10 Concentration

In this section, the temporal variation in PM10 at the three stations is discussed. The annual PM10 mean values were examined in the period from 2007–2017 (2009–2017 in the case of Pécs). Comparing the sites, we can conclude that the PM10 values are generally the highest in Miskolc and lowest in Pécs, while Budapest is characterized by an intermediate level of air pollution. In 2011, PM10 peaked at all stations; not surprisingly, the winter this year was unusually cold; the number of frosty days was the highest (102 days on average) during the entire time period (2007-2017). A local maximum was observed in 2017; this year, two extensive poor air quality episodes (affecting an extended region in Europe (Tarrason et al., 2018)) occurred from 20th to 30th January and from 9th to 17th February 2017. The event in January also included a sea salt episode (Tarrason et al., 2018). Both events were associated with high background PM2.5 concentrations and an important contribution from long-range transport (Tarrason et al., 2018). Hungary was also part of both events that had an effect on the annual average PM10 concentrations in 2017.

The number of exceedances of the EU air quality standard for daily average (the threshold of 50 µg m3 for the 24-hour average PM10 mass concentration) is also reported (note: the standard should not be exceeded more than 35 times during a year (EU Directive, 2008)). Unlike the annual average PM10 limits, this threshold was exceeded in almost all years in Budapest and Miskolc. Not surprisingly, most of the exceedances occurred during the winter and fall months (Fig. 1). The data in Fig. 1 show that at all stations, the number of exceedances exhibits a slight downward trend. Only two years, 2011 and 2017, are out of line, which is consistent with our previous explanation.

In Fig. 2, the average diurnal variations in the PM10 concentrations on weekdays and weekends are presented. In summer, the PM10 concentrations tend to be somewhat lower during weekends than during weekdays, while at night, the concentrations are rather similar. At the Miskolc site, the impact of transport is dominated on PM10, since this station is a traffic site as clearly indicated by the morning rush hours on weekdays. At the other two sites, the effect of the morning rush hour on the PM10 concentration is negligible compared to the evening PM10 maximum since these two sites correspond to urban background monitoring sites.

Fig. 2. Diurnal variation in the averaged PM10 concentrations in Budapest (Gilice tér), Miskolc (Búza tér), and Pécs (Boszorkány utca) (averaged over the 11-year period from 2007–2017).Fig. 2. Diurnal variation in the averaged PM10 concentrations in Budapest (Gilice tér), Miskolc (Búza tér), and Pécs (Boszorkány utca) (averaged over the 11-year period from 2007–2017).

In winter, a significant difference in the PM10 concentration was found when working and weekend days were compared. In Miskolc, the impact of residential heating is comparable to that of traffic emissions (EMEP/CEIP), which is the reason why the effect of morning rush hour is less important. Independent of the seasons, at all stations, an evening peak is typically found probably due to the unfavourable dispersion situation in this part of the day. The evening peak in winter is much higher, presumably as a result of indoor heating. The shift of the morning peak at Miskolc by about one hour from summer to winter can be explained by the shift to daylight savings time in Hungary.

The observations show that in every season, the highest PM10 concentrations can be expected in the morning and evening hours, while the minimum concentrations were measured between 11 and 15 hours. In winter, during this time period, the contribution of residential heating was not remarkable because people spent their time in public institutions fuelled by natural gas (Muntean et al., 2017).

3.2. Spectral Decomposition of Time Series

Local meteorological conditions exert a strong influence over day-to-day variations in PM10 concentrations; therefore, the meteorological signal must be removed for air quality planners and managers to examine the underlying emissions-related trends and make better air quality management decisions for the future. In this part of the study, a Kolmogorov-Zurbenko (KZ) filter was used to spectrally decompose the PM10 time series between 2007 and 2017 into different forcings controlled by different atmospheric processes that influence the measured PM10 concentrations. The Kolmogorov-Zurbenko (KZ) filter can be used to separate the time series of short-term components (influenced by the prevailing meteorological conditions) and baseline components (influenced by the emissions and boundary conditions) (Kang et al., 2013).

The KZ filter is based on Rao and Zurbenko’s statement and was described in detail by Wise and Comrie (2005). It is well documented that there is an obvious link between meteorological conditions and the air pollution level. Meteorological variability could overwhelm the effects of changes in pollutant emissions. To properly assess the changes in air concentration due to emission changes or air quality measures, the influence of short-term meteorological variability should be eliminated. Application of the KZ filter was first tested for tropospheric ozone issues, and it was later extended to regional PM and NO2 problems (Sá et al., 2015). A time series of air quality data can be represented by


where A(t) is the original time series, e(t) is the long-term trend component, S(t) is the seasonal variation, and W(t) is the short-term component. Baseline components are defined as the sum of the long-term and seasonal components.


The KZ filter is a low-pass filter derived from repeated iterations of a moving average. In our study, the daily mean PM10 concentration values were used. KZ(15,5) denotes the filter with a 15-day length and five iterations, and KZ(365,3) denotes the filter with a 365-day length and three iterations. The moving average for a KZ(m,p) filter (a filter with window length m and p iterations according to Sá et al. (2015)) is defined by


where k is the number of values included on each side of the targeted value, the window length is m = 2k + 1, and A is the input time series. The separation of the original air quality time series into the three components (long-term, seasonal, and short-term) for the daily average PM10 is presented in Fig. 3. The short-term component is attributable to weather and short-term fluctuations in precursor emissions (random effect), the seasonal component is a result of changes, for example, in the boundary layer height (effects that have typical seasonal variability), and the long-term trend results from changes in overall emissions, atmospheric transport, and climate.

Fig. 3. Decomposition of a daily average PM10 time series by the Kolmogorov-Zurbenko (KZ) filter into long-term, seasonal, and short-term components. Fig. 3. Decomposition of a daily average PM10 time series by the Kolmogorov-Zurbenko (KZ) filter into long-term, seasonal, and short-term components.

Table 1. Contribution of each component to the total variance in the original PM10 concentration.

The effect of the local weather conditions is reflected in the short-term component. These effects are random and can change from place to place, but they may have a significant impact on the daily variability in PM10 concentrations. The effect of this component is the most important among the three components during the winter months for all three Hungarian cities. The short-term variations in Budapest and Pécs exhibit relative maxima in January 2011 and a secondary maximum in January 2017 (Fig. 3), which can be explained by a strong atmospheric inversion over the whole Carpathian Basin. In January 2017 an extreme maximum of the short-term component can be observed in Miskolc. This study also confirms that poor air quality situations in Hungary are generally connected to special meteorological conditions.

In the case of the seasonal component, we found a strong relationship with the boundary layer height and the temperature since these two parameters show typical seasonality. In the case of a low boundary layer height, the mixing properties in the lower atmosphere are very poor and cause the accumulation of PM. When the temperature is below 0°C, the emission from residential heating increases.

The long-term trend results are related to changes in emissions. There are large differences between the long-term components of the three examined cities. No significant decrease in the long-term component concentration values occurs in Budapest. In the case of Miskolc and Pécs, the decreasing trend can be explained by the implementation of several measures regarding PM10 levels. In Miskolc, the cement industry was phased out in 2011 with the aim of reducing the level of pollutant release. This study also demonstrates the need for more local measures to improve the air quality in these cities.

To understand the contribution of each temporal component to the original daily average PM10 concentration value, the variance in each generated time series was determined, and their contributions to the total variance in the original data were calculated (Table 1).

3.3. Relationship between PM10 and Meteorological Parameters

The importance of the short-term component, containing the day-to-day variability due to weather, demonstrated that the meteorological parameters affect the PM10 concentrations in Hungary. To investigate the relationship between PM10 concentrations and meteorological variables, first, the correlation coefficients between daily meteorological variables such as temperature, wind speed, relative humidity, atmospheric pressure, global radiation, and boundary layer height, and daily PM10 were determined (Table 2).

Table 2. Correlation coefficients between PM10 and several meteorological parameters.

Although the relationship between meteorological parameters and PM10 is rather complex, we found some strong relationships between them. Positive (RH, p, and GR) and negative (T, WS, and PBL) correlations were found between several meteorological parameters and PM10 values for the whole year. The seasonality of the correlation between PM10 and the meteorological parameters was analysed separately, and large differences were found between the seasons. See Table 2 for the correlation values.

The highest negative values of the correlation coefficient can be observed with temperature, wind speed, and boundary layer height in the winter period. Significant seasonality can be observed in the case of temperature and relative humidity. In summer, the correlation with temperature resulted in a positive value, while in other seasons, a negative value of the correlation coefficient was observed. This suggests that in summer, heat might lead to poor air quality due to increasing concentrations of secondary PM10. The correlation with temperature changed from positive to negative (from summer to autumn, respectively). The explanation of the special behaviour of temperature can be connected with the seasonal variability of the usage of solid fuel (wood and coal). In summer, there is no residential combustion, while the intensity of heating is the greatest in winter when the usage of solid fuel is determinative in Hungary.

In the case of relative humidity, the situation was opposite in summer and spring, with a negative correlation coefficient, while in the other times of the year, a positive correlation coefficient was found. The moderate negative correlation suggested that in spring and summer, the high relative humidity was likely the result of precipitation; therefore, the PM10 concentration was reduced by wet deposition. On the one hand, the strong wind flushes the fine fraction of the PM out of the system, and on the other hand, it can increase the coarse fraction concentration, as a result of the more intense suspension of particles from ground surfaces. (Chaloulakou et al., 2003; Kukkonen et al., 2005; Zhang et al., 2018). A negative correlation between PM10 and boundary layer height likely resulted in significantly low dispersion and dilution of air pollutants. This fact demonstrates that meteorological conditions play an important role in the development of air pollution episodes.

Vardoulakis and Kassomenos (2008) obtained similar relationships and found correlation coefficients in the case of temperature (–0.24) and wind speed (–0.55) in the Birmingham Centre during cold conditions.

Multiple linear regression analysis has been used in the field of air pollution by several authors (Gupta and Christopher, 2009; Vlachogianni et al., 2011; Lin et al., 2012; Garcia et al., 2016). In our work, a regression method was applied for only winter because the strongest correlation between meteorological variables (temperature, wind speed, and boundary layer height) and PM10 was observed in this season, and the highest PM10 concentration level occurred in winter, which we wanted to predict.

Based on the results of the determination of the correlation coefficients, many meteorological parameters were selected for the regression analysis. Table 3 shows the obtained R2 values for the three most important meteorological parameters. In the case of temperature, the relationship was linear, while the boundary layer height and wind speed resulted in much better R2 values when a logarithmic relation was supposed. These results indicated that nonlinear multiple regression should be applied to predict the PM10 concentration.

Table 3. The R2 values for several meteorological parameters in winter.

The primary aim of our regression analysis was to determine the meteorological situations in which the PM10 concentration was expected to exceed the 50 µg m3 concentration threshold. The studies presented so far helped us to determine the most important meteorological factors that had an essential effect on the PM10 concentration in the winter period. In the development of the method, we assumed that the emissions were constant each day in winter and that the actual PM10 concentration was controlled by the weather. Unfortunately, we did not have exact information about how the emission of PM10 from domestic heating changed from day to day. We only assumed that this effect could be driven by the air temperature, but we could not determine its measure. This was the reason why we did not take into account the effect of emission changes in this method.

As a result of the analysis of the correlation coefficients, it was possible to predict the daily average PM10 concentration. In our case, the dependent variable that we wanted to predict was the PM10 concentration, and the independent variables were the temperature (T), wind speed (WS), and boundary layer height (PBL). The data analysis suggested that the best result could be obtained by fitting the nonlinear model to the meteorological variables. Several multiplicative regression models were tested to find the best-fitting model. Based on the evaluations of different models, the proposed regression formula was the following:


The summarized results of the regression (Table 4) confirmed that the proposed model could adequately predict the PM10 values. The overall test statistics indicated the significance of our model, i.e., high F statistics for 3 variables, and given degrees of freedom along with the zero p-values for the null hypothesis test indicated that all the model coefficients were equal to zero.

Table 4. Summary of the evaluation of the regression.

From the regression formula (Eq. (6)), the equation that predicts the daily average PM10 concentration is:


where α0 α1 α2 α3 are the multiple regression coefficients, T is the temperature (°C), PBL is the boundary layer height (m), and WS is the wind speed (m s1).

In Table 5, we summarized the corresponding parameters of the prediction in Eq. (7) for the three sites studied in this paper. To evaluate the equation performance, we tested it on an independent database (December 1, 2018–February 28, 2019). During the validation of the regression equation, the predicted PM10 values were compared with the corresponding PM10 measurements. Time series of the observed and predicted PM10 concentrations for the Budapest, Miskolc, and Pécs stations are presented in Fig. 4. The temporal variations in the curves are similar for most of the predicted and observed values. We recognize that extremely high observed daily mean concentrations were underpredicted in most of the cases with this method.

Table 5. Multiple regression coefficients and R2 values for predicting the PM10 concentration

Fig. 4. Observed and predicted daily average PM10 concentrations at the Budapest, Pécs, and Miskolc stations during the winter period.Fig. 4. Observed and predicted daily average PM10 concentrations at the Budapest, Pécs, and Miskolc stations during the winter period.

Several statistical scores, such as bias (BIAS), mean absolute error (MAE), root mean square error (RMSE) and R2, were determined to evaluate the regression equation. The second group of scores focuses on the prediction of PM10 exceedances at the threshold (50 µg m–3) and includes indices based on a contingency table. These indices are the probability of detection (POD) and false alarm ratio (FAR). Table 6 shows the results of the evaluation statistics.

Table 6. Evaluation statistics for forecasting.

The classical statistical scores (BIAS, MAE, RMSE) indicate that the regression equation provided the best results in Pécs. In Budapest, the determination coefficient (R2) was the highest (R2 = 0.48), while in Pécs and Miskolc, it was low but acceptable (0.34 and 0.25, respectively). The POD and FAR values were determined for the threshold value of 50 µg m–3. These indicators were the best in Miskolc. The result of the validation showed a mixed picture, and it would be very difficult to determine the station with the best results from the regression equation. Our method exhibited the best result for Miskolc when the goal was to predict whether the PM10 concentration would exceed the 50 µg m–3 concentration threshold limit.

Finally, it must be mentioned that in the case of Budapest, the locations of the meteorological instruments and air quality monitors are the same. Unfortunately, the situations in Pécs and Miskolc are different, and the meteorological station is 500–1000 m from the air quality monitoring station. This fact could influence the results of the multiple regression analysis.


In this paper, the effects of meteorological parameters on PM10 concentrations and their temporal behaviours were examined using monitoring data from different cities in Hungary. Several statistical indicators (average, temporal variation, correlation, regression) were determined to assess the characteristics of the PM10 pollution levels in these cities.

The yearly, monthly, weekly, and daily variations in the PM10 time series were determined using the data from three large cities in Hungary where the air quality is problematic. In the case of yearly averages, no limit value exceedances (40 µg m–3) were detected after 2011. However, analysing the daily average, the most limit value exceedances could be expected in winter and fall. There were large differences between the cities, and the air quality varied between moderate and poor in both Pécs and Miskolc. There were large variances year after year, which could be controlled by the meteorological conditions. Essential differences were not found between the characteristics of the weekly variations. In summer, the daily variation in PM10 was very similar in Budapest and Pécs, but in Miskolc, we found a characteristic peak in the morning that could be attributed to local traffic. In winter, the daily variation in PM10 from every station had the same features. We assumed that in the case of Miskolc, the effect of residential combustion was higher than the effect of traffic, so the peak originating from morning traffic could not be identified. We concluded that no significant variability in the average PM10 concentrations was found throughout a week. In each city, there was a slight increase from Monday to Friday, and then a pronounced decline was observed during the weekend. A difference between the mean weekly concentration values in the individual cities was clearly observable.

Variations in the concentration levels of PM10 could be decomposed to a baseline component of pollution created by emission sources and to other components controlled by meteorological conditions. The Kolmogorov-Zurbenko (KZ) filter is a useful tool for the investigation of the interactions between emissions, meteorological conditions, and air quality levels. The PM10 long-term component has the lowest contribution (only 1–6%) to the variance observed in the original data. On the other hand, the short-term component has the highest contribution to the total variance in the original data. In Budapest, the contribution of the short-term component to the total variance in the original data is the highest and is more than 10% higher than that in Miskolc. The contribution of the seasonal component is the highest in Miskolc, approximately 10% higher than that in Budapest.

We also analysed the evolution of urban PM10 concentrations in terms of the relevant meteorological parameters. Correlation analysis was carried out to identify the most important meteorological variables influencing the PM10 concentration in Hungary. As a result of this analysis, the highest PM10 concentrations were clearly related to the decreasing air temperature, lowering PBL height, and weakening wind speed during winter. The effect of temperature on the PM10 concentration was likely to be very complex. Low temperature and poor vertical mixing could be observed together in winter; at the same time, low temperature induced an increase in the usage of solid fuel, which resulted in increased PM10 emissions from domestic heating.

Multiple regression analysis was used to determine the connection between the concentration of PM10 and specific meteorological parameters: temperature, planetary boundary layer height, and wind speed. The results of this study showed that the relationship between PM10 and each meteorological parameter was acceptable (the R2 values in the regression formula were 0.57, 0.49, and 0.43), and the model that was built could be used for PM10 prediction. Our method did not take into account the daily changes in PM10 emissions. We assumed that the emissions were constant on each day of the winter season. After model validation, it could be stated that our constructed statistical model could be effectively used to decide whether the daily mean PM10 values were expected to exceed the 50 µg m–3 threshold value.


This work was supported by GINOP-2.3.2-15-2016-00055 Project through the National Research, Development and Innovation Office, Hungary.

The authors would like to thank Péter Németh for helpful guidance in KZ filtering.


  1. Barmpadimos, I., Hueglin, C., Keller, J., Henne, S., Prévôt, A.S.H. (2011). Influence of meteorology on PM10 trends and variability in Switzerland from 1991 to 2008. Atmos. Chem. Phys. 11, 1813–1835. https://doi.org/10.5194/acp-11-1813-2011

  2. Barmpadimos, I., Keller, J., Hueglin, C., Prevot, A.S.H. (2012). One decade of parallel fine (PM2.5) and coarse (PM10-PM2.5) particulate matter measurements in Europe: trends and variability. Atmos. Chem. Phys. 12, 3189. https://doi.org/10.5194/acp-12-3189-2012

  3. Chaloulakou, A., Kassomenos, P., Spyrellis, N., Demokritou, P., Koutrakis, P. (2003). Measurements of PM10 and PM2.5 particle concentrations in Athens, Greece. Atmos. Environ. 37, 649–660. https://doi.org/10.1016/S1352-2310(02)00898-1

  4. Chen, Z., Xie, X., Cai, J., Chen, D., Gao, B., He, B., Cheng, N., Xu, B. (2018). Understanding meteorological influences on PM2.5 concentrations across China: A temporal and spatial perspective. Atmos. Chem. Phys. 18, 5343–5358. https://doi.org/10.5194/acp-18-5343-2018

  5. De Marco, A., Proietti, C., Anav, A., Ciancarella, L., D'Elia, I., Fares, S., Fornasierb, M.F., Fusaroe, L., Manese, M.G.F., Marchettof, A., Mirceac, M., Paolettig, E., Piersantic, A., Rogoraf, M., Salvatid, L., Salvatorie, E., Screpantih, A., Vialettoc, G., Vitalee, M., Leonardi, C. (2019). Impacts of air pollution on human and ecosystem health, and implications for the National Emission Ceilings Directive: Insights from Italy. Environ. Int. 125, 320–333. https://doi.org/10.1016/j.envint.2019.01.064

  6. Demuzere, M., Trigo, R.M., Vila-Guerau de Arellano, J., Van Lipzig, N. (2009). The impact of weather and atmospheric circulation on O3 and PM10 levels at a rural mid-latitude site. Atmos. Chem. Phys. 9, 2695–2714. https://doi.org/10.5194/acp-9-2695-2009

  7. Diapouli, E., Manousakas, M.I., Vratolis, S., Vasilatou, V., Pateraki, S., Bairachtari, K.A., Querol, X., Amato, F., Alastuey, A., Karanasiou, A.A., Lucarelli, F., Nava, S., Calzolai, G., Gianelle, V.L., Colombi, C., Alves, C., Custódio, D., Pio, C., Spyrou, C., Kallos, G.B., Eleftheriadis, K. (2017). AIRUSE-LIFE +: estimation of natural source contributions to urban ambient air PM10 and PM2.5 concentrations in southern Europe – implications to compliance with limit values. Atmos. Chem. Phys. 17, 3673–3685. https://doi.org/10.5194/acp-17-3673-2017

  8. Directive EU (2008). 2008/50/EC of the European Parliament and of the Council of 21 May 2008 on ambient air quality and cleaner air for Europe. OJ L 152, 11.6.2008, 1–44. http://data.europa.eu/eli/dir/2008/50/oj

  9. Directive EU (2016). 2016/2284 of the European Parliament and of the Council of 14 December 2016 on the reduction of national emissions of certain atmospheric pollutants, amending Directive 2003/35/EC and repealing Directive 2001/81/EC.

  10. Dunea, D., Iordache, S., Ianache, C. (2015). Relationship between airborne particulate matter and weather conditions in Târgoviște urban area during cold months. Rev. Roumaine Chimie 60, 595–601.

  11. EMEP/CEIP. Emissions as used in EMEP models. (accessed 13 May 2021).

  12. European Environment Agency (2019). Air quality in Europe 2019, EEA Report No 10/2019.

  13. Fang, Y., Naik, V., Horowitz, L.W., Mauzerall, D.L. (2013). Air pollution and associated human mortality: The role of air pollutant emissions, climate change and methane concentration increases from the preindustrial period to present. Atmos. Chem. Phys. 13, 1377–1394. https://doi.org/10.5194/acp-13-1377-2013

  14. Ferenczi, Z., Bozó, L. (2017). Effect of the long-range transport on the air quality of greater Budapest area. Int. J. Environ. Pollut. 62, 407–416. https://doi.org/10.1504/IJEP.2017.089428

  15. Ferenczi, Z., Homolya, E., Bozó, L. (2020) Detailed Assessment of a Smog Situation Detected in the Sajó Valley, Hungary. in: Mensink C., Gong W., Hakami A. (Eds.), Air Pollution Modeling and its Application XXVI. ITM 2018. Springer Proceedings in Complexity. Springer, Cham. https://doi.org/10.1007/978-3-030-22055-6_56

  16. Garcia, J.M., Teodoro, F., Cerdeira, R., Coelho, L.M.R., Kumar, P., Carvalho, M.G. (2016). Developing a methodology to predict PM10 concentrations in urban areas using generalized linear models. Environ. Technol. 37, 2316–2325. https://doi.org/10.1080/09593330.2016.1149228

  17. Guerreiro, C.B., Foltescu, V., De Leeuw, F. (2014). Air quality status and trends in Europe. Atmos. Environ. 98, 376–384. https://doi.org/10.1016/j.atmosenv.2014.09.017

  18. Gupta, P., Christopher, S.A. (2009). Particulate matter air quality assessment using integrated surface, satellite, and meteorological products: Multiple regression approach. J. Geophys. Res. 114, D14205. https://doi.org/10.1029/2008JD011496

  19. Horvath, H. (1995). Estimation of the average visibility in central Europe. Atmos. Environ. 29, 241–246. https://doi.org/10.1016/1352-2310(94)00236-E

  20. Jancsek-Turóczi, B., Hoffer, A., Nyírő-Kósa, I., Gelencsér, A. (2013). Sampling and characterization of resuspended and respirable road dust. J. Aerosol Sci. 65, 69–76. https://doi.org/10.1016/j.jaerosci.2013.07.006

  21. Kang, D., Hogrefe, C., Foley, K.L., Napelenok, S.L., Mathur, R., Rao, S.T. (2013). Application of the Kolmogorov–Zurbenko filter and the decoupled direct 3D method for the dynamic evaluation of a regional air quality model. Atmos. Environ. 80, 58–69. https://doi.org/10.1016/j.atmosenv.2013.04.046

  22. Karagulian, F., Belis, C.A., Dora, C.F.C., Pruss-Ustun, A.M., Bonjour, S., Adair-Rohani, H., Amann, M. (2015). Contributions to cities' ambient particulate matter (PM): A systematic review of local source contributions at global level. Atmos. Environ. 120, 475–483. https://doi.org/10.1016/j.atmosenv.2015.08.087

  23. Kis-Kovács, G., Tarczay, K., Lovas, K., Ludányi, E.L., Nagy, E., Kőbányai, K. (2019). Informative Inventory Report of Hungary 1990-2017. https://pm10.kormany.hu/download/f/15/62000/IIR_HU_2019_v1.pdf

  24. Kukkonen, J., Pohjola, M., Sokhi, R. S., Luhana, L., Kitwiroon, N., Fragkou, L., Rantamäki, M., Berge, E., Ødegaard, V., Slørdal, L.H., Denby, B., Finardi, S. (2005). Analysis and evaluation of selected local-scale PM10 air pollution episodes in four European cities: Helsinki, London, Milan and Oslo. Atmos. Environ. 39, 2759–2773. https://doi.org/10.1016/j.atmosenv.2004.09.090

  25. Kuzmichev, A.A., Loboyko, V.F. (2016). Impact of the polluted air on the appearance of buildings and architectural monuments in the area of town planning. Procedia Eng. 150, 2095–2101. https://doi.org/10.1016/j.proeng.2016.07.244

  26. Lim, S.S., Vos, T., Flaxman, A.D., Danaei, G., Shibuya, K., Adair-Rohani, H., Aryee, M. (2012). A comparative risk assessment of burden of disease and injury attributable to 67 risk factors and risk factor clusters in 21 regions, 1990–2010: A systematic analysis for the Global Burden of Disease Study 2010. Lancet 380, 2224–2260. https://doi.org/10.1016/S0140-6736(12)61766-8

  27. Lin, M., Tao, J., Chan, C.Y., Cao, J.J., Zhang, Z.S., Zhu, L.H., Zhang, R.J. (2012). Regression analyses between recent air quality and visibility changes in megacities at four haze regions in China. Aerosol Air Qual. Res. 12, 1049–1061. https://doi.org/10.4209/aaqr.2011.11.0220

  28. Menut, L., Goussebaile, A., Bessagnet, B., Khvorostiyanov, D., Ung, A. (2012). Impact of realistic hourly emissions profiles on air pollutants concentrations modelled with CHIMERE. Atmos. Environ. 49, 233–244. https://doi.org/10.1016/j.atmosenv.2011.11.057

  29. Muntean, M., Janssens-Maenhout, G., Guizzardi, D., Crippa, M., Schaaf, E., Poljanac, M., Logar, M., Zemko, M., Cristea-Gassler, C. (2017). Impact evaluation of biomass used in small combustion activities sector on air emissions: Analyses of emissions from Alpine, Adriatic-Ionian and Danube EU macro-regions by using the EDGAR emissions inventory. JRC109332, Publications Office of the European Union, Luxembourg.

  30. Pearce, J.L., Beringer, J., Nicholls, N., Hyndman, R.J., Tapper, N.J. (2011). Quantifying the influence of local meteorology on air quality using generalized additive models. Atmos. Environ. 45, 1328–1336. https://doi.org/10.1016/j.atmosenv.2010.11.051

  31. Perrone, M.G., Vratolis, S., Georgieva, E., Török, S., Šega, K., Veleva, B., Osán, J., Bešlić, I., Kertész, Z., Pernigotti, D., Eleftheriadis, K., Belis, C.A. (2018). Sources and geographic origin of particulate matter in urban areas of the Danube macro-region: The cases of Zagreb (Croatia), Budapest (Hungary) and Sofia (Bulgaria). Sci. Total Environ. 619, 1515–1529. https://doi.org/10.1016/j.scitotenv.2017.11.092

  32. Sá, E., Tchepel, O., Carvalho, A., Borrego, C. (2015). Meteorological driven changes on air quality over Portugal: A KZ filter application. Atmos. Pollut. Res. 6, 979–989. https://doi.org/10.1016/j.apr.2015.05.003

  33. Seinfeld, J.H., Pandis, S.N. (2012). Atmospheric chemistry and physics: from air pollution to climate change. John Wiley & Sons.

  34. Tarrasón, L., Hamer, P.D., Meleux, F., Rouïl, L. (2018). Interim Annual Assessment Report for 2017, CAMS report 2018. 

  35. Thunis, P., Degraeuwe, B., Peduzzi, E., Pisoni, E., Trombetti, M., Vignati, E., Wilson, J., Belis, C., Pernigotti, D. (2017). Urban PM2.5 Atlas: Air Quality in European cities, EUR 28804 EN, Publications Office of the European Union, Luxembourg. https://doi.org/10.2760/336669

  36. Tidblad, J., Kreislová, K., Faller, M., De la Fuente, D., Yates, T., Verney-Carron, A., Grøntoft, T., Gordon, A., Hans, U. (2017). ICP Materials Trends in Corrosion, Soiling and Air Pollution (1987–2014). Materials 10, 969. https://doi.org/10.3390/ma10080969

  37. van der Gon, H.A.C., Bergström, R., Fountoukis, C., Johansson, C., Pandis, S.N., Simpson, D., Visschedijk, A.J. (2015). Particulate emissions from residential wood combustion in Europe revised estimates and an evaluation. Atmos. Chem. Phys. 15, 6503–6519. https://doi.org/10.5194/acp-15-6503-2015

  38. Van Dingenen, R., Raes, F., Putaud, J.P., Baltensperger, U., Charron, A., Facchini, M.C., Decesari, S., Fuzzi, S., Gehrig, R., Hansson, H.C., Harrison, R.M., Hüglin, C., Jones, A.M., Laj, P., Lorbeer, G., Maenhaut, W., Palmgren, F., Querol, X., Rodriguez, S., Schneider, J., Ten Brink, H., Tunved, P., Tørseth, K., Wehner, B., Weingartner, E., Wiedensohler, A., Wåhlin, P. (2004). A European aerosol phenomenology - 1: Physical characteristics of particulate matter at kerbside, urban, rural and background sites in Europe. Atmos. Environ. 38, 2561–2577. https://doi.org/10.1016/j.atmosenv.2004.01.040

  39. Vardoulakis, S., Kassomenos, P. (2008). Sources and factors affecting PM10 levels in two European cities: Implications for local air quality management. Atmos. Environ. 42, 3949–3963. https://doi.org/10.1016/j.atmosenv.2006.12.021

  40. Velders, G.J., Matthijsen, J. (2009). Meteorological variability in NO2 and PM10 concentrations in the Netherlands and its relation with EU limit values. Atmos. Environ. 43, 3858–3866. https://doi.org/10.1016/j.atmosenv.2009.05.009

  41. Vlachogianni, A., Kassomenos, P., Karppinen, A., Karakitsios, S., Kukkonen, J. (2011). Evaluation of a multiple regression model for the forecasting of the concentrations of NOx and PM10 in Athens and Helsinki. Sci. Total Environ. 409, 1559–1571. https://doi.org/10.1016/j.scitotenv.2010.12.040

  42. Wise, E.K., Comrie, A.C. (2005). Extending the Kolmogorov–Zurbenko filter: Application to ozone, particulate matter, and meteorological trends. J. Air Waste Manage. Assoc. 55, 1208–1216. https://doi.org/10.1080/10473289.2005.10464718

  43. Zhang, B., Jiao, L., Xu, G., Zhao, S., Tang, X., Zhou, Y., Gong, C. (2018). Influences of wind and precipitation on different-sized particulate matter concentrations (PM2.5, PM10, PM2.5-10). Meteorol. Atmos. Phys. 130, 383–392. https://doi.org/10.1007/s00703-017-0526-9 

Share this article with your colleagues 


Subscribe to our Newsletter 

Aerosol and Air Quality Research has published over 2,000 peer-reviewed articles. Enter your email address to receive latest updates and research articles to your inbox every second week.

77st percentile
Powered by
   SCImago Journal & Country Rank

2022 Impact Factor: 4.0
5-Year Impact Factor: 3.4

Aerosol and Air Quality Research partners with Publons

CLOCKSS system has permission to ingest, preserve, and serve this Archival Unit
CLOCKSS system has permission to ingest, preserve, and serve this Archival Unit

Aerosol and Air Quality Research (AAQR) is an independently-run non-profit journal that promotes submissions of high-quality research and strives to be one of the leading aerosol and air quality open-access journals in the world. We use cookies on this website to personalize content to improve your user experience and analyze our traffic. By using this site you agree to its use of cookies.