Next Article in Journal
An Upscaling Method for Cover-Management Factor and Its Application in the Loess Plateau of China
Previous Article in Journal
West Nile Virus Transmission in Sentinel Chickens and Potential Mosquito Vectors, Senegal River Delta, 2008–2009

Int. J. Environ. Res. Public Health 2013, 10(10), 4728-4751; doi:10.3390/ijerph10104728

Acute and Subacute Effects of Urban Air Pollution on Cardiopulmonary Emergencies and Mortality: Time Series Studies in Austrian Cities
Manfred Neuberger 1, Hanns Moshammer 1,* and Daniel Rabczenko 2
Institute of Environmental Health, Medical University of Vienna, A-1090 Kinderspitalgasse 15, Austria
National Institute of Public Health – National Institute of Hygiene, PL-00-791 Warsaw, ul. Chocimska 24, Poland
Author to whom correspondence should be addressed; Tel.: +43-1-40160-34935; Fax: +43-1-40160-934903.
Received: 4 July 2013; in revised form: 29 September 2013 / Accepted: 29 September 2013 / Published: 2 October 2013


: Daily pollution data (collected in Graz over 16 years and in the Linz over 18 years) were used for time series studies (GAM and case-crossover) on the relationship with daily mortality (overall and specific causes of death). Diagnoses of patients who had been transported to hospitals in Linz were also available on a daily basis from eight years for time series analyses of cardiopulmonary emergencies. Increases in air pollutant levels over several days were followed by increases in mortality and the observed effects increased with the length of the exposure window considered, up to a maximum of 15 days. These mortality changes in Graz and Linz showed similar patterns like the ones found before in Vienna. A significant association of mortality could be demonstrated with NO2, PM2.5 and PM10 even in summer, when concentrations are lower and mainly related to motor traffic. Cardiorespiratory ambulance transports increased with NO2/PM2.5/PM10 by 2.0/6.1/1.7% per 10 µg/m3 on the same day. Monitoring of NO2 (related to motor traffic) and fine particulates at urban background stations predicts acute effects on cardiopulmonary emergencies and extended effects on cardiopulmonary mortality. Both components of urban air pollution are indicators of acute cardiopulmonary health risks, which need to be monitored and reduced, even below current standards.
air pollution; particulate matter; nitrogen dioxide; emergencies; mortality; time series

1. Introduction

In most European cities PM10 and NO2 are used for surveillance of air quality, under the assumption that these air pollutants predict health effects best. NO2 is monitored as the surrogate of motor traffic exhaust, which is measured more easily than ultrafine particles. However, it is still unclear whether NO2 only modifies effects of PM10 on mortality [1] or if it is a key indicator of motor traffic and its health effects [2,3,4]. Recently European cities have in addition monitored PM2.5, because a limit was set for its annual concentration, however, a standard for daily PM2.5 concentration is still missing in Europe. Some health effects were found more closely related to NO2 [5,6] which is more variable with distance to road and correlated with black carbon and ultrafines, in particular from diesel soot.

In multicentre studies similar associations between daily PM10 exposures and cardiorespiratory mortality were found in Europe and the United States [7,8]. Mortality increase with PM10, however, was higher in Canada [9], while in Europe most pronounced mortality effects were seen in warmer cities with higher NO2 and a larger NO2/PM10 ratio [10]. This pattern was less pronounced in the United States, where the proportion of diesel cars is lower.

In Austria 55% of passenger cars and nearly all vans and trucks use diesel engines, because of the relatively low price of diesel fuel. In the capital Vienna a 10 µg/m3 change in PM2.5 was associated with a 2.6% change of daily mortality and a 10 µg/m3 change in NO2 with a 2.9% change of daily mortality, lagged 0–14 days. The increase of mortality [11] and hospital admissions [12,13] with PM and NO2 was seen in Vienna even in years without violation of EU standards (PM10 annual average 40 µg/m3, PM10 daily average 50 µg/m3 exceeded on not more than 35 days per year; NO2 hourly average 200 µg/m3 with maximal 18 exceedances per year). The present study investigates the associations of TSP, PM10, PM2.5, NO2, SO2 and O3 concentrations with daily mortality in a longer time series, in Graz, the 2nd largest and in Linz, the 3rd largest Austrian city, sharing similar populations and car fleets. The goal was to verify the results from Vienna in smaller cities and to find the best indicators for the prediction of short-term effects of urban air pollution on specific mortality. In addition to previously used generalized additive models (GAM), a case-crossover approach is used for the evaluation of air pollutant effects outside the heating season, to enable conclusions on motor traffic. As an additional outcome, cardiopulmonary emergencies transported to hospitals were available for a shorter time period in the city of Linz. These cases are also analysed in a case-crossover approach.

2. Study Population and Methods

The city of Graz is situated south of the Alps in a semi alpine basin, with only very little industrial emissions. Nevertheless the EU standard for PM10 is exceeded regularly in winter, because of weak natural ventilation, long lasting inversions and stagnant weather conditions, when a locally aged aerosol forms from motor traffic and domestic heating [14,15]. Similar to Vienna, the city of Linz is located north of the Alps on the Danube, where air exchange is much better, resulting in lower ambient air pollution in winter, despite of a heavy industry conglomerate (iron, steel, chemistry). Like in Vienna SO2 had been reduced in both cities to low concentrations before 1990, leaving particulate matter (from traffic and heating) and NO2 (dominated by diesel powered vehicles) as the key pollutants [16], with data available after quality checks from 1990 to 2005 in Graz and from 1990 to 2007 in Linz. We used daily concentrations of pollutants (averaged over all available stations) as measures of exposure.

In Graz the number of inhabitants is only 261,540 (15% in comparison to Vienna) and in Linz 189,367 (11% in comparison to Vienna). From power calculations [17] we therefore had to choose longer time series than in Vienna, starting 1990. Methods used for monitoring of air pollutants and for modelling of missing data have been described earlier [12,15]. In short, time series from monitoring stations were used, which showed the highest correlation with all other urban background stations. Missing data were replaced by linear regression from the station with the second highest correlation to all other stations. In Graz exposure estimation was based on routine data of six stations, with five urban background stations monitoring TSP and NO2 since 1990. PM10 was monitored at these stations since 2000 and PM2.5 in 2000–2001 at one station only. Before 2000 PM10 was modelled from station specific relations to TSP and meteorological parameters. PM2.5 could not be modelled in Graz, because relations to measured values were available only for a single year and a single station.

In Linz exposure estimation for the period 1990–2007 was based on six stations, four of them monitoring TSP and NO2 since 1990, PM10 since 2000 and one station monitoring PM2.5 in 2000–2001 and since 2005. Earlier missing data on PM2.5 were modelled from TSP. SO2, O3 and meteorological data were available for the complete period of observation in both cities. In Linz no sentinel data on influenza were available like in Vienna and Graz. In Graz sentinel data on influenza (registered 1990–2005 weekly and during epidemics daily) were used to adjust for the confounder of influenza epidemics, defined by an increase of incidence to >3,500 cases per week. Associations of air pollutants with hospital admissions (together with diagnoses at discharge) had been analysed in both cities before [12,13]. The present time series on daily mortality incidence in Graz and Linz used the same ICD-classes, overdispersed Poisson GAMs and lags (lag 0–1 day and polynomial distributed lags 0–7 and 0–14 days), which had been used in the Vienna study [11]. From death certificates the main or underlying cause of death is usually based on hospital diagnoses and high autopsy rates [18], ensuring a high diagnostic quality. Total mortality was analysed as well as deaths from specific causes, namely cardiovascular and respiratory diseases. In addition total mortality in the elderly (aged 65+) was investigated because this group might be more sensitive to effects of air pollution [19].

The model contained the following confounders: long-term trend and seasonality, day of the week, period of influenza epidemics and meteorological variables. The analysis started from building a base model without the air pollution variables. Thereby it was determined, what best described variability of daily mortality using all confounders. Day of the week and periods of influenza epidemics were modelled with dummy variables, other confounders were modelled using spline functions [20]. First the appropriate number of knots for the cubic regression spline representing long-term trend and seasonal variations was sought by minimising the sum of partial autocorrelation over 40 days [9]. Next meteorological factors were sequentially entered to the model: temperature, atmospheric pressure, humidity and changes of temperature and pressure between consecutive days. Different lags (0–3) and varying degrees of freedom were considered. Choice of lag structure was based on the Akaike Information Criterion [21].

Several aspects of air pollution effect on mortality were taken into account. The acute effect was modelled using linear and logarithmic function of mean of current and previous days. In addition the concentration-effect was further modelled as a spline function. Cumulative effects and a possible harvesting effect were investigated through a 3rd degree of polynomial distributed lag model. We also contemplated non-linear pollutant effects for the distributed lag model [22,23], but because the pollutants’ effects were fairly linear we abstained from these for the sake of interpretability. Difference in magnitude of air pollution effect by season (warm/cold) and level of other pollutants (high/low) were examined by creating appropriate dummy variables to be included in interaction terms. All computations were done using R 2.5.0 software applying the mgcv package for GAMs. For interactions between NO2 and PM at lag 0–1 we used models with interaction of PM10 and high NO2 and NO2 and high PM10, defining “high” as the median or above.

In Linz morbidity data were also available from eight years: daily emergency transports to hospitals had been registered and diagnoses encoded in 2000–2007. This period in Linz was too short for stable results on mortality by GAM because of the small population and a high correlation between daily temperature and fine particulate concentration [17]. Therefore a case-crossover approach [24] was chosen, both for cardiopulmonary emergency transports and for cardiopulmonary and total deaths: exposures on case days were compared by conditional logistic regression with those on referent days occurring on a day with the most similar temperature (less than 1 °C difference) in the same season [25,26,27,28]. To eliminate time trends we chose a bi-directional approach and a time window of 7–21 days before and after the case (two referent days for each day of occurrence). This way temperature and season were eliminated as confounders and an overlap between periods of occurrence and referent periods was prevented. The time window of 7–21 days was narrow enough to find a day with equal temperature in the same season and it left a minimum distance of seven days to the occurrence day of cases at lag 0. This minimum distance was reduced to six days by analysing lags of one day, but it was not possible to analyse distributed lags of 0–7 days and 0–14 days without overlap of occurrence days and referent days. Therefore only short latencies could be analysed in the case-crossover study.

3. Results

Daily means of particulate matter and NO2 registered in Graz at five background stations and in Linz at three background stations and one roadside station are shown in Table 1. The distributions of the key pollutants PM10 and NO2 were similar, with higher median of NO2 in Linz (38 µg/m3) than in Graz (32 µg/m3), but lower 95th percentile in Linz (62 µg/m3) than in Graz (68 µg/m3). The median/95th percentile of PM10 was slightly higher in Linz (32/86 µg/m3) compared to Graz (29/73 µg/m3). The median/95th percentile of TSP in Graz were 39/100 µg/m3 and the median/95th percentile of PM2.5 in Linz were 19/49 µg/m3.

SO2 concentrations were low most of the time (except for the first two winters observed in Graz): in Graz the median/95th percentile was 7/30 µg/m3 and in Linz 5/19 µg/m3. Ozone was constantly higher during summer (especially during the last summer seasons observed), but had been monitored at elevated locations (Graz 348 m, 450 m and 661 m; Linz 265 m and 335 m), which were not representative for the exposures in domestic areas, where PM and NO2 had been monitored. In Graz the median/95th percentile) was 49/96 µg/m3 and in Linz 41/86 µg/m3.

Table 1. Descriptive statistics of pollution concentrations (µg/m3) and health effects (average per day).
Table 1. Descriptive statistics of pollution concentrations (µg/m3) and health effects (average per day).
(A) NO2Graz 1990–2005Linz 1990–2007Linz 2000–2007Vienna 2000–2004
Arithm. mean35.739.434.623.0
Std. dev.17.013.313.110.7
5th percentile15.120.616.59.0
25th percentile24.
75th percentile43.347.241.129.1
95th percentile68.562.258.043.0
(B) TSPGraz 1990–2005Linz 1990–2007Linz 2000–2007Vienna 2000–2004
Arithm. mean45.8--30.6
Std. dev.26.8--16.1
5th percentile16.6--12
25th percentile27.4--19
75th percentile56.5--39
95th percentile100.2--61
(C) PM10Graz 1990–2005Linz 1990–2007Linz 2000–2007Vienna 2000–2004
Arithm. mean34.038.133.3130.2
Std. dev.19.326.612.919.0
5th percentile12.411.110.59
25th percentile20.720.418.416.8
75th percentile42.048.342.839.0
95th percentile73.485.873.866.8
(D) PM2.5Graz 1990–2005Linz 1990–2007Linz 2000–2007Vienna 2000–2004
Arithm. mean-22.420.516.3
Std. dev.-15.012.910.5
5th percentile-7.17.15
25th percentile-12.511.78.9
75th percentile-27.925.620.6
95th percentile-49.345.936.2
(E) End-pointsGraz 1990–2005Linz 1990–2007Linz 2000–2007Vienna 2000–2004
Total deaths6.95.65.443.9
Ambulance calls--15.7-
MethodGAMGAMCase cross-overGAM

Most deaths occurred on Mondays and least on Sundays. Mortality rates were highest in winter. When in sensitivity analysis degrees of freedom for the seasonal variation were increased the effect estimates for the pollutants were reduced, as was to be expected. But the impact of moderate changes in the degrees of freedom was only minimal (data not shown). Among the weather parameters temperature had the strongest effect both on mortality (in a typical u-shaped form) and on the estimates of the pollutants’ effects. Indeed in most of the full models SO2 seemed to be protective, which had been kept in the model as a sort of negative control despite of its low concentrations, for some endpoints and lags even significantly so, at least in Vienna and Linz. This implausible finding was removed or even reversed when temperature was not included in the models. This could eventually indicate some over-adjustment by temperature and was one of the reasons to stratify by temperature in the case-crossover models applied for the shorter time-series in Linz.

Figure 1. Per cent change in daily mortality, with 95% confidence intervals, in Graz (G) 1990–2005 and Linz (L) 1990–2007 per 10 µg/m3 increase in the respective pollutant measure over the preceding 2, 8, and 15 days (lag 0–1, lag 0–7, lag 0–14). Corresponding data [11] of Vienna (V) are shown for comparison.
Figure 1. Per cent change in daily mortality, with 95% confidence intervals, in Graz (G) 1990–2005 and Linz (L) 1990–2007 per 10 µg/m3 increase in the respective pollutant measure over the preceding 2, 8, and 15 days (lag 0–1, lag 0–7, lag 0–14). Corresponding data [11] of Vienna (V) are shown for comparison.
Ijerph 10 04728 g001 1024

Figure 1 and Supplemental Table S1 give effect estimates for daily overall mortality. Results for special age groups and selected causes of death are also presented in Supplemental Table S1. Results from the Vienna study [11] are included for comparison. The temporal distribution of effect estimates is exemplified for several mortality end-points in Graz in Supplemental Figure S1. Simpler models measuring the average exposure over 8 or 15 days instead of calculating the additive effects of 8 or 15 days distributed lags gave rather similar cumulative results (data not shown).

In all three cities significant increases of mortality are seen with daily NO2 and fine particle mass. No significant changes were found for SO2 and O3 (data not shown). After an increase of NO2 or PM total mortality increases cumulatively with latency. Mortality increase was highest per µg/m3 for NO2. In Graz a mortality increase of 2.6% (3.2% in males and 2.1% in females) was found per 10 µg/m3 of NO2 for a lag of 0–14 days. Mortality increased less per µg/m3 of PM10 and TSP, but significantly. Also in Linz significant increases of mortality for lags 0–7 and 0–14 days were observed, related to NO2 (highest per µg/m3), PM2.5 and PM10 (lowest per µg/m3). Except for a higher effect of NO2 in Linz at lag 0–7 all pollutants show the highest effect at lag 0–14, indicating cumulative effects. Higher effects at longer lags are also seen in the results per interquartile range, with the highest estimate per IQR of NO2. None of the interaction terms between NO2 and PM10 was found to be significant in Graz and in Linz (data not shown).

Missing data on PM10 and PM2.5 had been inferred from other measured pollutants for periods of several years and these estimates were pooled with measured data. We did sensitivity analyses to justify this procedure by investigating the interaction of PM effects with a dummy variable for the periods in which PM10 was calculated from TSP or PM2.5 from PM10. Results for the main effects of the pollutant remained unchanged (both coefficient value and its significance), both dummy variable and interaction term were statistically not significant.

The mortality increase was significant in both cities for males and females, for the elderly and for cardiopulmonary diseases. Also for specific causes of death the highest estimates were found at a lag of 0–14 days, with highest mean estimates for respiratory deaths (COPD in particular), followed by cardiovascular deaths, which reached 2.4% per 10 µg/m3 of NO2 in both cities at lag 0–14. In Graz at a lag of 0–7/0–14 days a mean increase of 2.9%/4.0% per 10 µg/m3 was estimated for deaths from ischemic heart diseases (IHD) related to NO2 and 3.7%/4.3% related to PM10. The corresponding figures for deaths from respiratory diseases (RD) were 8.1%/12.3% related to NO2 and 3.4%/5.1% related to PM10. Increases in Linz were lower, for RD in particular, with cardiovascular deaths more related to NO2. However, all results for deaths from IHD and RD were also in Linz significantly related to NO2 and PM10 at longer latencies (IHD at lag 0–7 and 0–14, and RD at lag 0–14). Daily deaths from gastrointestinal diseases (used for control in the time series) did not show any associations with air pollutant concentrations in Graz and Linz (data not shown).

As a sensitivity analysis in Linz the period since 2000 (Figure 2) was studied separately when PM10 was measured directly and no longer had to be calculated from TSP [15]. The key pollutants measured in Linz from 2000 to 2007 showed a similar distribution of concentrations like in Vienna from 2000 to 2004.

To exclude any effects from exposures to domestic heating (wood smoke), separate mortality analyses were run outside the heating seasons from June 1st to August 31st over eight years. Both approaches (case-crossover and GAM) estimate elevations of mortality after short latency (up to one day). Despite of the shorter time period available for the case-crossover analysis and the limitation to summer months, confidence intervals were found narrower than in the full period analysed by GAM. Per µg/m3 the effect on total mortality on the same day was highest for PM2.5. But the case-crossover model yields significant elevations of mortality also for NO2 and PM10 of the same and the preceding summer day.

Figure 2. Effect estimates in Linz 2000–2007: Per cent change in daily mortality, with 95% confidence interval, per 10 µg/m3 increase in the respective pollutant measure. Full diamonds: Estimates from the years 2000–2007 on the same and on preceding day (lag 0 and lag 1), case-crossover model for the summer season (1st June to 31st August). For comparison Poisson GAM (open diamonds): estimates from the years 1990–2007 (full years) for the average of the same and preceding day (lag 0–1).
Figure 2. Effect estimates in Linz 2000–2007: Per cent change in daily mortality, with 95% confidence interval, per 10 µg/m3 increase in the respective pollutant measure. Full diamonds: Estimates from the years 2000–2007 on the same and on preceding day (lag 0 and lag 1), case-crossover model for the summer season (1st June to 31st August). For comparison Poisson GAM (open diamonds): estimates from the years 1990–2007 (full years) for the average of the same and preceding day (lag 0–1).
Ijerph 10 04728 g002 1024
Table 2. Per cent increase in ambulance calls (with 95% confidence intervals) related to a 10 µg/m3 increase in the respective pollutant measure. Linz (2000–2007).
Table 2. Per cent increase in ambulance calls (with 95% confidence intervals) related to a 10 µg/m3 increase in the respective pollutant measure. Linz (2000–2007).
Lag 0 dayLag 1 dayLag 2 days
All cardiopulmonary2.0 (0.8; 3.2)−3.5 (−4.6; −2.4)-
Cardiovascular1.2 (−0.4; 2.8)−4.2 (−5.7; −2.6)−1.0 (−2.5; 0.6)
Respiratory2.3 (−0.5; 5.1)−3.2 (−5.9; −0.6)0.3 (−2.4; 3.0)
Unclear cause3.4 (1.2; 5.6)−3.2 (−5.3; −1.0)−0.1 (−2.3; 2.1)
All cardiopulmonary6.1 (4.3; 7.8)0.1 (−1.4; 1.7)
Cardiovascular7.1 (4.7; 9.4)0.3 (−1.8; 2.4)2.5 (0.3; 4.7)
Respiratory2.1 (−2.1; 6.3)−1.6; −5.2; 2.0)1.0 (−2.7; 4.7)
Unclear cause3.7 (0.4; 7.0)0.4 (−2.5; 3.4)3.4 (0.3; 6.4)
All cardiopulmonary1.7 (1.0; 2.3)0.0 (−0.6; 0.6)
Cardiovascular1.3 (0.9; 2.6)−0.5 (−0.9; 0.7)0.5 (0.1; 1.8)
Respiratory2.7 (1.2; 4.2)1.3 (−0.1; 2.7)1.0 (−0.4; 2.5)
Unclear cause1.6 (0.9; 3.3)0.0 (−0.7; 1.6)0.9 (0.2; 2.5)

In the case-crossover model significant elevations of cardiopulmonary emergencies (Table 2) were found related to NO2, PM2.5 and PM10, but not to O3. Per µg/m3 morbidity effects at lag 0 were most pronounced for PM2.5. No significant associations of cardiopulmonary emergencies or mortality were found with SO2 (data not shown). At lag 1 NO2, PM2.5 and PM10 appeared to be protective indicating a sort of “harvesting” effect.

4. Discussion

The association of cardiopulmonary morbidity and mortality with PM, NO2 and proximity to road are likely to share the same biological mechanisms: fine and ultrafine particles from combustion entering the lung, pulmonary reflexes over the autonomic nervous system affecting heart rate and arrhythmia, pulmonary inflammation, systemic inflammation from ultrafines entering the blood stream, endothelial dysfunction, reactive oxygen species, activation of leucocytes, platelets and other coagulation factors.

Health effects of air pollution are often classified into short- and long-term effects, although there is most probably a continuum of effects on the time scale, not yet completely understood. The results in Graz and Linz confirm earlier observations in Vienna [11], that prolonged mortality effects are higher than immediate effects, indicating that latent and cumulative effects outweigh harvesting (reduction of mortality after short increase due to premature deaths of most sensitive persons). Time series studies in Vienna had also found increases of respiratory hospital admissions related to PM2.5 [12] and of mortality from cardiovascular, cerebrovascular and respiratory diseases related to PM10, PM2.5 and NO2, most pronounced for a lag period of 15 days [12]. A time-series of daily hospital admissions in Vienna, Graz and Linz predicted the highest increases of cardiovascular admissions per µg/m3 for PM1, followed by PM2.5 and PM10, and also significant associations with daily NO2 concentrations were found [13]. The present study in Linz supplements, that also cardiopulmonary emergency transports in ambulance cars (preceding hospital admissions) rise quickly with daily concentrations of PM2.5, PM10 and NO2. In Vienna overall and cardiovascular mortality increased with latency and reached highest values per µg/m3 of NO2, followed by PM2.5. The same was found for overall mortality in Graz and Linz (Figure 1) and for cardiopulmonary mortality, indicating that legally binding limit values of daily PM10 might be less important than limitation of fine and ultrafine particles associated with NO2.

As an advantage of the time-series approach [29,30] the same population is used as exposed (on high pollution days) and as “control” (on low pollution days). Therefore no confounding by individual characteristics is probable. In contrast to cohort studies, time series are not confounded by risks spatially correlated to air pollution like traffic noise [31]. Daily means of urban air pollution are rather dependent on meteorological factors and day of the week (controlled in the present study) than on daily means of traffic noise, the socio-economic status or the daily dose of tobacco smoke (unrelated in time to ambient air pollution).

Differences between the three largest Austrian cities have to be examined in cohort studies, but we think that the present study found more similarities than differences of results. Differences in attribution of underlying cause of death to pulmonary or cardiovascular disease in elderly persons could be influenced by local diagnostic and coding peculiarities; however, overall mortality is mainly influenced by the age distribution of the population, which was found to be very similar in Graz, Linz and Vienna [18]. Interactions of outdoor pollution with effects of active and passive smoking cannot be excluded; however, the same regulations apply for tobacco control in the three cities and smoking rates in 2006–2007 were similar [32]: Graz 20.9% (males 28.2%, females 14.2%) Linz 22.5% (males 23.2%, females 21.9%), Vienna 24.6% (males 30.3%, females 19.6%). A speculative explanation for the smaller effect of PM10 on mortality in Linz is the short distance of one of the stations in Linz to a tunnel portal of a busy road, where higher concentrations were measured than in domestic areas, possibly leading to an overestimation of mean exposure and an underestimation of the slope in the concentration-response relationship.

In Linz a very quick rise of cardiopulmonary emergencies was observed with NO2, PM2.5 and PM10, even in summer (without heating) at levels below current standards. Together with the results on mortality this acute increase of cardiopulmonary morbidity indicates that urban air pollution is still a matter of concern and confirms the demand to lower PM2.5 standards and to introduce a limit value for the daily mean of PM2.5 in the European Union [33].

Figure 3. Per cent change in daily mortality, with 95% confidence intervals, in Graz (1990–2005), related to pollutants’ concentration over the same and the preceding day (lag 0–1). Degrees of freedom: 3.1 (TSP), 3.3 (PM10), 5.4 (NO2).
Figure 3. Per cent change in daily mortality, with 95% confidence intervals, in Graz (1990–2005), related to pollutants’ concentration over the same and the preceding day (lag 0–1). Degrees of freedom: 3.1 (TSP), 3.3 (PM10), 5.4 (NO2).
Ijerph 10 04728 g003 1024

In Graz a significant increase of total mortality was seen already at short latencies with TSP and PM10, below a daily PM10 concentration of 50 µg/m3, which is the EU limit for the daily mean. This increase of mortality was steep at concentrations below the current standard of PM10 and flattened above (Figure 3). At very high concentrations we observed a second increase; however, the estimate from rare events is unreliable, as can be seen from the widening confidence intervals at high concentrations. What could be concluded from the concentration-response function is the absence of a threshold, as found by other investigators [8,34], but questions also the present regulations: Figure 3 seems to contradict the current methods of surveillance of daily PM10 concentrations with reporting of the number of exceedances of 50 µg/m3 per year: From short-term mortality effects in Graz it seems to be of low relevance if the PM10 concentration is a little below or above the standard of 50 µg/m3. On the other hand considerable health benefits are expected from reductions of pollutants also at locations where and at times when concentrations are very much below the current standard. For NO2 the concentration-response function shows an increase of short-term mortality in the concentration range of about 25 to 90 µg/m3. The estimate gets unreliable at very low and especially at very high concentrations, but from Figure 3 no indication for a threshold higher than 25–30 µg/m3 can be seen. On the other hand, also these effects level off, when daily means of about 35 µg/m3 are exceeded, but this flattening of the curve is only seen up to about 50 µg/m3, which is frequently exceeded due to motor traffic at urban background stations in domestic areas. Most pronounced are the prolonged effects of NO2 on mortality, which can hardly be explained by the gas itself. More likely NO2 is a surrogate for ultrafine particles from motor traffic and diesel exhaust in particular. Therefore this study supports demands for a better surveillance of traffic-related pollutants. Emission concentrations of ultrafine particles are regulated already in the EU [35].

The results of the present study contribute to the “suggestive evidence of a causal relationship” between exposure to traffic-related air pollution and total (mainly cardiovascular) mortality [8]: NO2 indicates combustion and motor traffic. The contribution of motor traffic to PM increases with decreasing particle size. Therefore the effects on mortality, most pronounced per µg/m3 of NO2 and increasing with decreasing particle size of PM in Graz, Linz and Vienna, indicate health effects of motor traffic. In all three cities NO2 is mainly of local origin, also in summer [36]. By contrast, in Linz and Vienna about 60% of PM10 is imported [37], while in Graz PM10 is also mainly of local origin, with a high traffic share [38]. Even in Linz the contribution of the industry to NO2 exposure of the population is small and in Graz it is negligible. In contrast to studies in more industrialized areas [39], we therefore think that the results on NO2-related health effects in this study allow conclusions on health effects of motor traffic and diesel engines in particular. Up to now studies on proximity to roads [40,41] are unable to say, which part of health effects are related to the irritant gas NO2 itself, to accompanying ultrafine particles or to traffic noise, which had also been suggested as a risk factor for cardiovascular diseases [42], or to other spatially correlated risk factors. For PM also Goodman et al. [43] observed that extended effects of air pollution exceed its acute effects. To our knowledge there are no studies on subacute mortality and NO2, however, in cohort studies higher cumulative effects had been found after much longer latencies for both PM [39,40] and NO2 [3,4].

Data on PM10 were not available before 2000 and had to be modelled from TSP and meteorology. Nevertheless PM10 effects were found to exceed those of TSP, as expected. PM2.5 had been monitored in Graz and Linz in 2000–2001 and in Linz since 2005. Despite of the necessity to model the PM2.5 concentrations in Linz from PM10 in 2002–2004 and from TSP in earlier years, PM2.5 was found to predict cardiopulmonary emergencies and mortality (Figure 1) very well.

Separate time series over the summer months did not reveal a significant effect of ozone on mortality, but significant elevations related to NO2, PM2.5 and PM10. This underlines the importance of motor traffic exhaust for acute effects on mortality in urban environments. The absence of mortality effects related to ozone was also observed in Vienna [11] and might be due to the sampling strategy in all three cities, which was different from other pollutants: Ozone was not monitored in densely populated areas like PM10, NO2 and SO2, but at elevations and downwind of urban precursor emissions, where few people lived. We cannot exclude small effects of O3 on respiratory mortality in summer months, detectable only in larger cities. A longer time series from Vienna with sufficient power could recently show ozone effects on mortality [43] using data of a central station.

SO2 effects were not seen in Graz, Linz and Vienna during the available person-years of observation, however, already before the begin of this study, during the 1980s, Austria had achieved the highest SO2 reduction among the signatory states of the Helsinki Protocol [12] and these low concentrations over most of the observation period, could explain the lack of association of SO2 with mortality.

For Vienna emissions of NO2 were estimated to decrease [44] from 2010 to 2020 by 513 tons only (road traffic NO2 from 1,590 to 1,090 tons per year). During the same decade a reduction of PM10 by 240 tons was estimated (road traffic from 770 to 570 tons per year). This does not give hope for a disappearance of related health effects in the near future.

5. Conclusions

The concentrations of NO2 and small particles predicted health effects of urban air pollution in the three largest cities of Austria very well. Therefore we see no necessity at present to supplement surveillance by other indicators of combustion and motor traffic such as black carbon [45,46] or ultrafine particles [47]. Changing motor technology (direct injection, etc.) and fuel-additives, however, could possibly require additional indicators of ambient air pollution in the future.

From the results in Graz and Linz we conclude, that also smaller cities face acute health effects of air pollution from local motor traffic. This study supports the conclusion [12,33] that more stringent standards need to be adopted in Europe to protect public health from ambient PM2.5 and it adds, that also further reductions of NO2 might be necessary on local, national and EU level, accompanied by epidemiological studies.


The study in Graz was financially supported by the government of Styria, department of health (Odo Feenstra) and the study in Linz by the government of Upper Austria, department of environment (Elisabeth Danninger).

Conflicts of Interest

The authors declare no conflict of interest.


  1. Samoli, E.; Analitis, A.; Touloumi, G.; Schwartz, J.; Anderson, H.R.; Sunyer, J.; Bisanti, L.; Zmirou, D.; Vonk, J.M.; Pekkanen, J.; et al. Estimating the exposure-response relationships between particulate matter and mortality within the APHEA multicity project. Environ. Health Perspect. 2005, 113, 88–95. [Google Scholar]
  2. Lambrechtsen, J.; Gerke, O.; Egstrup, K.; Sand, N.P.; Nørgaard, B.L.; Petersen, H.; Mickley, H.; Diederichsen, A.C. The relation between coronary artery calcification in asymptomatic subjects and both traditional risk factors and living in the city centre: A DanRisk substudy. J. Intern. Med. 2012, 271, 444–450. [Google Scholar] [CrossRef]
  3. Naess, O.; Nafstad, P.; Aamodt, G.; Claussen, B.; Rosland, P. Relation between concentration of air pollution and cause-specific mortality: Four-year exposures to nitrogen dioxide and particulate matter pollutants in 470 neighborhoods in Oslo, Norway. Am. J. Epidemiol. 2007, 165, 435–443. [Google Scholar]
  4. Nafstad, P.; Haheim, L.L.; Wisloff, T.; Gram, F.; Oftedal, B.; Holme, I.; Hjermann, I.; Leren, P. Urban air pollution and mortality in a cohort of Norwegian Men. Environ. Health Perspect. 2004, 112, 610–615. [Google Scholar] [CrossRef]
  5. Chen, R.; Samoli, E.; Wong, C.M.; Huang, W.; Wang, Z.; Chen, B.; Kan, H.; CAPES Collaborative Group. Associations between short-term exposure to nitrogen dioxide and mortality in 17 Chinese cities: The China Air Pollution and Health Effects Study (CAPES). Environ. Int. 2012, 45, 32–38. [Google Scholar] [CrossRef]
  6. Lenters, V.; Uiterwaal, C.S.; Beelen, R.; Bots, M.L.; Fischer, P.; Brunekreef, B.; Hoek, G. Long-term exposure to air pollution and vascular damage in young adults. Epidemiology 2010, 21, 512–520. [Google Scholar] [CrossRef]
  7. HEI (Health Effects Institute), Revised Analyses of Time-Series Studies of Air Pollution and Health; MA Health Effects Institute: Boston, MA, USA, 2003.
  8. HEI (Health Effects Institute), Traffic-Related Air Pollution. A Critical Review of the Literature on Emissions, Exposure, and Health Effects; Special Report 17; MA Health Effects Institute: Boston, MA, USA, 2010.
  9. Samoli, E.; Peng, R.; Ramsay, T.; Pipikou, M.; Touloumi, G.; Dominici, F.; Burnett, R.; Cohen, A.; Krewski, D.; Samet, J.; Katsouyanni, K. Acute effects of ambient particulate matter on mortality in Europe and North America: Results from the APHENA study. Environ. Health Perspect. 2008, 116, 1480–1486. [Google Scholar] [CrossRef]
  10. Samoli, E.; Touloumi, G.; Zanobetti, A.; Le Tertre, A.; Shindler, C.; Atkinson, R.; Vonk, J.; Rossi, G.; Saez, M.; Rabczenko, D.; et al. Investigating the dose-response relation between air pollution and total mortality in the APHEA-2 multicity project. Occup. Environ. Med. 2003, 60, 977–982. [Google Scholar] [CrossRef]
  11. Neuberger, M.; Rabczenko, D.; Moshammer, H. Extended effects of air pollution on cardiopulmonary mortality in Vienna. Atmos. Environ. 2007, 41, 8549–8556. [Google Scholar] [CrossRef]
  12. Neuberger, M.; Schimek, M.G.; Horak, F.; Moshammer, H.; Kundi, M.; Frischer, T.; Gomiscek, B.; Puxbaum, H.; Hauck, H.; AUPHEP-Team. Acute effects of particulate matter on respiratory diseases, symptoms and functions. Epidemiological results of AUPHEP. Atmos. Environ. 2004, 38, 3971–3981. [Google Scholar] [CrossRef]
  13. Neuberger, M.; Schimek, M.G.; Moshammer, H.; Hauck, H.; Kofler, W. Fine particulates and hospital admissions in Graz, Linz, and Vienna. Atemw. Lungenkrht. 2008, 34, 387–390. (in German). [Google Scholar] [CrossRef]
  14. Almbauer, R.; Pucher, K.; Sturm, P.J. Air quality modeling for the city of Graz. Meteorol. Atmos. Environ. 2005, 57, 31–42. [Google Scholar] [CrossRef]
  15. Hauck, H.; Berner, A.; Frischer, T.; Gomiscek, B.; Kundi, M.; Neuberger, M.; Puxbaum, H.; Preining, O.; AUPHEP-Team. Austrian project on health effects of particulates—General overview. Atmos. Environ. 2004, 38, 3905–3915. [Google Scholar] [CrossRef]
  16. Spangl, W.; Nagl, C. Annual Report of Air Quality Measurements in Austria 2010; (in German). Environment Agency Austria: Vienna, Austria, 2011; pp. 48–53. [Google Scholar]
  17. Winquist, A.; Klein, M.; Tolbert, P.; Sarnat, S. Power estimation using simulations for air pollution time-series studies. Environ. Health 2012, 11. [Google Scholar] [CrossRef]
  18. Statistik Austria, Demographic Yearbook 2008; (in German). Statistik Austria: Vienna, Austria, 2009.
  19. Cakmak, S.; Dales, R.E.; Rubio, M.A.; Vidal, C.B. The risk of dying on days of higher air pollution among the socially disadvantaged elderly. Environ. Res. 2011, 111, 388–393. [Google Scholar] [CrossRef]
  20. Baccini, M.; Biggeri, A.; Lagazio, C.; Lertxundi, A.; Saez, M. Parametric and semi-parametric approaches in the analysis of short-term effects of air pollution on health. Comput. Statist. Data Anal. 2007, 51, 4324–4336. [Google Scholar] [CrossRef]
  21. Akaike, H. Information theory as an extension of the maximum likelihood principle. In Proceedings of the Second International Symposium on Information Theory; Petrov, B.N., Csaki, B.F., Eds.; Akademiai Kiado: Budapest, Hungary, 1973; pp. 267–281. [Google Scholar]
  22. Gasparrini, A.; Armstrong, B. Time series analysis on the health effects of temperature: Advancements and limitations. Environ. Res. 2010, 110, 633–638. [Google Scholar] [CrossRef]
  23. Goldberg, M.S.; Gasparrini, A.; Armstrong, B.; Valois, M.-F. The short-term influence of temperature on daily mortality in the temperate climate of Montreal, Canada. Environ. Res. 2011, 111, 853–860. [Google Scholar] [CrossRef]
  24. Carracedo-Martínez, E.; Taracido, M.; Tobias, A.; Saez, M.; Figueiras, A. Case-Crossover Analysis of Air Pollution Health Effects: A Systematic Review of Methodology and Application. Environ. Health Perspect. 2010, 181, 1173–1182. [Google Scholar]
  25. Schwartz, J. The effects of particulate air pollution on daily deaths: A multi-city case crossover analysis. Occup. Environ. Med. 2004, 61, 956–961. [Google Scholar] [CrossRef]
  26. Schwartz, J. How sensitive is the association between ozone and daily deaths to control for temperature? Am. J. Respir. Crit. Care Med. 2005, 171, 627–631. [Google Scholar] [CrossRef]
  27. Zanobetti, A.; Schwartz, J. Air pollution and emergency admissions in Boston, MA. J. Epidemiol. Community Health 2006, 60, 890–895. [Google Scholar]
  28. Scheers, H.; Mwalili, S.M.; Faes, C.; Fierens, F.; Nemery, B.; Nawrot, T.S. Does air pollution trigger infant mortality in Western Europe? A case-crossover study. Environ. Health Perspect. 2011, 119, 1017–1022. [Google Scholar] [CrossRef]
  29. Zheng, S.; Wang, M.; Wang, S.; Tao, Y.; Shang, K. Short-Term Effects of Gaseous Pollutants and Particulate Matter on Daily Hospital Admissions for Cardio-Cerebrovascular Disease in Lanzhou: Evidence from a Heavily Polluted City in China. Int. J. Environ. Res. Public Health 2013, 10, 462–477. [Google Scholar] [CrossRef]
  30. Zhang, F.; Li, L.; Krafft, T.; Lv, J.; Wang, W.; Pei, D. Study on the Association between Ambient Air Pollution and Daily Cardiovascular and Respiratory Mortality in an Urban District of Beijing. Int. J. Environ. Res. Public Health 2011, 8, 2109–2123. [Google Scholar] [CrossRef]
  31. Allen, R.W.; Davies, H.; Cohen, M.A.; Mallach, G.; Kaufman, J.D.; Adar, S.D. The spatial relationship between traffic-generated air pollution and noise in 2 US cities. Env. Res. 2009, 109, 334–342. [Google Scholar] [CrossRef]
  32. Klimont, J.; Kytir, J.; Leitner, B. Austrian Health Survey 2006/2007; (in German). Statistik Austria: Vienna, Austria, 2007. [Google Scholar]
  33. Ballester, F.; Medina, S.; Boldo, E.; Goodman, P.; Neuberger, M.; Iñiguez, C.; Künzli, N. Reducing ambient levels of fine particulates could substantially improve health: A mortality impact assessment for 26 European cities. J. Epidemiol. Community Health 2008, 62, 98–105. [Google Scholar] [CrossRef]
  34. WHO (World Health Organisation), Air Quality Guidelines for Particulate Matter, Ozone, Nitrogen Dioxide and Sulfur Dioxide—Global Update 2005—Summary of Risk Assessment; World Health Organisation: Geneva, Switzerland, 2006.
  35. Giechaskiel, B.; Mamakos, A.; Andersson, J.; Dilara, P.; Martini, G.; Schindler, W.; Bergmann, A. Measurement of Automotive Nonvolatile Particle Number Emissions within the European Legislative Framework: A Review. Aerosol Sci. Technol. 2012, 46, 719–749. [Google Scholar] [CrossRef]
  36. Kurz, C.; Sturm, P. Examination of the NO2 and PM10 Contamination in the Urban Area of Linz; (in German). Graz University of Technology: Graz, Austria, 2011. [Google Scholar]
  37. Kreindl, J.; Hager, W. Air Quality Data in 2010; Report 2/2011; (in German). Municipality of Linz, Environmental & Technical Center: Linz, Austria, 2011. [Google Scholar]
  38. Öttl, D. Modelling. Primary PM10 Concentrations for the City of Graz, Austria; Air Quality Department of Styria: Graz, Austria, 2008. [Google Scholar]
  39. Gehring, U.; Heinrich, J.; Kramer, U.; Grote, V.; Hochadel, M.; Sugiri, D.; Kraft, M.; Rauchfuss, K.; Eberwein, H.G.; Wichmann, H.E. Long-Term Exposure to Ambient Air Pollution and Cardiopulmonary Mortality in Women. Epidemiology 2006, 17, 545–551. [Google Scholar] [CrossRef]
  40. Hoek, G.; Brunekreef, B.; Goldbohm, S.; Fischer, P.; van den Brandt, P.A. Association between mortality and indicators of traffic-related air pollution in the Netherlands: A cohort study. Lancet 2002, 360, 1203–1209. [Google Scholar]
  41. Rosenbloom, J.I.; Wilker, E.H.; Mukamal, K.J.; Schwartz, J.; Mittleman, M.J. Residential proximity to major roadway and 10-Year all-cause mortality after myocardial infarction. Circulation 2012, 125, 2197–2203. [Google Scholar]
  42. Bluhm, G.; Eriksson, C. Cardiovascular effects of environmental noise: Research in Sweden. Noise Health 2011, 13, 212–216. [Google Scholar] [CrossRef]
  43. Goodman, P.G.; Dockery, D.W.; Clancy, L. Cause-specific mortality and the extended effects of particulate pollution and temperature exposure. Environ. Health Perspect. 2004, 112, 179–185. [Google Scholar] [CrossRef]
  44. Moshammer, H.; Hutter, H.-P.; Kundi, M. Which metric of ambient ozone to predict daily mortality? Atmos. Environ. 2013, 65, 171–176. [Google Scholar] [CrossRef]
  45. Kurz, C.; Orthofer, R.; Sturm, P.; Kaiser, A.; Uhrner, U.; Reifeltshammer, R. Projection of the air quality in Vienna between 2005 and 2020 for NO2 and PM10. In Proceedings of the 8th International Conference on Air Quality, Athens, Greece, 19-23 March 2012; p. 104.
  46. Dons, E.; Panis, L.I.; Van Poppel, M.; Theunis, J.; Wets, G. Personal exposure to Black Carbon in transport microenvironments. Atmos. Environ. 2012, 55, 392–398. [Google Scholar] [CrossRef]
  47. Janssen, N.A.H.; Gerlofs-Nijland, M.E.; Lanki, T.; Salonen, R.O.; Cassee, F.; Hoek, G. Health Effects of Black Carbon; WHO Regional Office for Europe: Copenhagen, Denmark, 2012. [Google Scholar]
  48. Wang, Y.; Hopke, P.K.; Chalupa, D.C.; Utell, M.J. Long-term study of urban ultrafine particles and other pollutants. Atmos. Environ. 2011, 45, 7672–7680. [Google Scholar] [CrossRef]

Supplemental Materials

Table S1. Lag-structure and degrees of freedom in the models. (A) Per cent increase in mortality (with 95% confidence intervals) related to a 10 µg/m3 increase in pollution—Vienna. (B) Per cent increase in mortality (with 95% confidence intervals) related to a 10 µg/m3 increase in pollution—Graz. (C) Per cent increase in mortality (with 95% confidence intervals) related to a 10 µg/m3 increase in pollution—Linz (1990–2007).
Table S1. Lag-structure and degrees of freedom in the models. (A) Per cent increase in mortality (with 95% confidence intervals) related to a 10 µg/m3 increase in pollution—Vienna. (B) Per cent increase in mortality (with 95% confidence intervals) related to a 10 µg/m3 increase in pollution—Graz. (C) Per cent increase in mortality (with 95% confidence intervals) related to a 10 µg/m3 increase in pollution—Linz (1990–2007).
(A) ViennaLag 0–1 dayLag 0–7 daysLag 0–14 days
All deaths0.8 (0.0; 1.6)2.1 (0.8; 3.5)2.9 (1.6; 4.1)
Cardiovascular0.7 (−0.4; 1.8)3.1 (1.2; 5.0)4.6 (2.9; 6.3)
Ischemic heart0.4 (−1.2; 1.9)2.8 (0.3; 5.3)4.5 (2.4; 6.6)
Other heart1.6 (−1.1; 4.5)4.6 (0.4; 9.1)3.9 (0.4; 7.6)
Cerebrovascular1.0 (−1.7; 3.9)2.4 (−1.8; 6.7)4.4 (0.8; 8.2)
Respiratory2.3 (−0.6; 5.2)5.7 (1.1; 10.6)6.7 (2.7; 10.8)
COPD1.9 (−2.4; 6.4)9.9 (3.0; 17.3)8.9 (3.0; 15.2)
All deaths0.3 (−0.3; 0.9)0.9 (−0.0; 1.9)0.8 (0.0; 1.6)
Cardiovascular0.3 (−0.5; 1.2)1.6 (0.3; 3.0)1.7 (0.7; 2.8)
Ischemic heart0.8 (−0.4; 2.1)2.6 (0.8; 4.5)3.4 (1.9; 4.9)
Other heart0.3 (−1.8; 2.4)0.9 (−2.2; 4.1)−1.3 (−3.7; 1.2)
Cerebrovascular0.1 (−2.0; 2.3)0.9 (−2.3; 4.1)1.7 (−0.9; 4.3)
Respiratory2.3 (0.0; 4.7)3.7 (0.1; 7.4)2.7 (−0.1; 5.6)
COPD3.6 (0.2; 7.1)8.5 (3.1; 14.2)5.0 (0.7; 9.4)
All deaths0.5 (−0.6; 1.5)1.8 (−0.0; 3.7)2.6 (1.1; 4.1)
Cardiovascular0.4 (−1.0; 1.8)2.7 (0.3; 5.2)3.8 (1.9; 5.8)
Ischemic heart1.0 (−1.0; 3.1)3.8 (0.6; 7.1)5.5 (3.0; 8.1)
Other heart0.9 (−2.6; 4.6)3.0 (−2.2; 8.5)1.5 (−2.5; 5.7)
Cerebrovascular0.4 (−3.2; 4.1)2.7 (−2.7; 8.4)4.9 (0.7; 9.3)
Respiratory3.9 (0.1; 7.8)7.0 (0.9; 13.4)6.4 (1.9; 11.2)
COPD6.4 (0.6; 12.5)14.0 (4.9; 24.0)9.0 (1.9; 16.6)
All deaths0.2 (−0.4; 0.7)0.9 (−0.1; 1.9)1.2 (0.4; 2.1)
Cardiovascular−0.2 (−0.6; 1.0)1.4 (0.1; 2.8)2.0 (0.9; 3.1)
Ischemic heart0.4 (−0.7; 1.6)2.1 (0.4; 3.9)3.2 (1.8; 4.6)
Other heart0.4 (−1.5; 2.4)1.3 (−1.6; 4.3)−0.1 (−2.4; 2.2)
Cerebrovascular0.3 (−1.6; 2.4)1.4 (−1.6; 4.4)2.6 (0.3; 5.0)
Respiratory2.1 (0.0; 4.2)3.5 (0.1; 6.9)3.0 (0.5; 5.5)
COPD3.5 (0.4; 6.7)7.9 (3.0; 12.9)5.1 (1.3; 9.1)
(B) GrazLag 0–1 dayLag 0–7 daysLag 0–14 days
All deaths1.2 (0.3; 2.2)2.0 (1.2; 2.9)2.6 (2.0; 3.1)
65+1.6 (−0.6; 3.8)2.0 (1.1; 2.9)1.9 (1.3; 2.5)
Before 651.2 (0.1; 2.3)2.6 (0.7; 4.5)2.5 (1.2; 3.9)
Male1.3 (0; 2.7)2.4 (1.2; 3.7)3.2 (2.3; 4.1)
Female1.1 (−0.2; 2.4)1.8 (0.7; 2.9)2.1 (1.3; 2.9)
Cardiovascular0.3 (−1.1; 1.7)1.9 (0.7; 3.0)2.4 (1.6; 3.2)
Ischemic heart0.5 (−1.6; 2.7)2.9 (1.1; 4.8)4.0 (2.7; 5.4)
COPD7.8 (2.2; 13.7)10.8 (5.9; 16.0)13.9 (10.3; 17.5)
Respiratory6.2 (1.7; 11.0)8.1 (4.1; 12.2)12.3 (9.5; 15.2)
All deaths0.9 (0.4; 1.5)1.2 (0.7; 1.7)1.2 (0.9; 1.5)
65+1.1 (−0.1; 2.3)1.2 (0.7; 1.7)0.1 (−0.3; 0.4)
Before 650.9 (0.3; 1.5)1.4 (0.3; 2.4)0.9 (0.2; 1.6)
Male1.1 (0.3; 1.9)1.5 (0.8; 2.2)1.5 (1.1; 2.0)
Female0.8 (0; 1.5)1.1 (0.5; 1.7)1.1 (0.6; 1.5)
Cardiovascular1.2 (0.5; 2.0)1.9 (1.2; 2.5)0.9 (0.4; 1.3)
Ischemic heart1.3 (0.1; 2.6)2.6 (1.5; 3.6)3.1 (2.4; 3.8)
COPD2.9 (−0.1; 6.0)3.7 (0.9; 6.4)4.0 (2.1; 5.9)
Respiratory1.9 (−0.6; 4.5)2.4 (0.2; 4.7)3.7 (2.2; 5.3)
All deaths1.3 (0.5; 2.1)1.5 (0.9; 2.2)1.6 (1.1; 2.0)
65+1.3 (−0.4; 3.1)1.5 (0.8; 2.2)0.3 (−0,1; 0.8)
Before 651.3 (0.4; 2.2)1.8 (0.4; 3.3)1.5 (0.5; 2.5)
Male1.4 (0.2; 2.5)1.8 (0.8; 2.8)2.0 (1.4; 2.7)
Female1.2 (0.1; 2.3)1.5 (0.6; 2.3)1.3 (0.8; 1.9)
Cardiovascular1.6 (0.6; 2.7)2.5 (1.6; 3.4)1.0 (0.4; 1.7)
Ischemic heart2.0 (0.2; 3.8)3.7 (2.3; 5.2)4.3 (3.2; 5.3)
COPD3.5 (−0.8; 7.9)4.3 (0.6; 8.2)4.6 (2.1; 7.2)
Respiratory2.8 (−0.8; 6.4)3.4 (0.4; 6.5)5.6 (3.5; 7.8)
(C) LinzLag 0–1 dayLag 0–7 daysLag 0–14 days
All deaths0.5 (−0.7; 1.6)2.0 (1.1; 3.0)1.5 (0.9; 2.2)
Cardiovascular0.1 (−1.5; 1.7)2.3 (0.9; 3.7)2.4 (1.5; 3.4)
Ischemic heart1.0 (−1.4; 3.4)3.8 (1.7; 5.9)2.5 (1.0; 3.9)
COPD1.1 (−4.1; 6.7)1.1 (−3.6; 6.0)1.5 (0.8; 2.3)
Respiratory1.9 (−2.3; 6.3)2.4 (−1.1; 6.0)2.5 (1.5; 3.5)
65 +0.4 (−0.9; 1.7)2.0 (0.9; 3.1)1.5 (0.7; 2.2)
Male1.2 (−0.3; 2.7)2.0 (0.6; 3.4)1.8 (0.8; 2.8)
Female0.0 (1.5; 1.5)1.9 (0.6; 3.1)1.9 (1.0; 2.8)
All deaths0.4 (−0.5; 1.3)0.8 (0.1; 1.6)1.2 (0.7; 1.7)
Cardiovascular0.5 (−0.7; 5.9)1.8 (0.7; 2.9)3.3 (2.5; 4.1)
Ischemic heart0.6 (−1.4; 2.6)2.1 (0.4; 3.8)2.0 (0.9; 3.2)
COPD1.3 (−2.9; 5.6)0.3 (−3.5; 4.4)1.3 (0.8; 1.9)
Respiratory2.5 (−0.7; 5.9)2.1 (−0.8; 5.0)3.6 (2.8; 4.3)
65 +0.7 (−0.4; 1.7)1.2 (0.3; 2.0)1.4 (0.9; 2.0)
Male0.4 (−0.8; 1.6)0.5 (−0.6; 1.6)0.8 (0.1; 1.6)
Female0.0 (−1.2; 1.2)0.6 (−0.4; 1.7)0.7 (0.0; 1.4)
All deaths0.2 (−0.3; 0.7)0.4 (0.0; 0.9)0.6 (0.4; 0.9)
Cardiovascular0.3 (−0.4; 1.0)1.1 (0.5; 1.7)2.0 (1.5; 2.4)
Ischemic heart0.4 (−0.7; 1.5)1.3 (0.4; 2.3)1.3 (0.7; 2.0)
COPD0.4 (−2.0; 2.8)0.0 (−2.2; 2.2)0.8 (0.5; 1.1)
Respiratory1.1 (−0.8; 2.9)1.0 (−0.6; 2.6)2.1 (1.7; 2.5)
65 +0.3 (−0.3; 0.8)0.7 (0.2; 1.1)0.9 (0.6; 1.2)
Male0.1 (−0.6; 0.8)0.2 (−0.4; 0.8)0.3 (−0.1; 0.7)
Female0.1 (−0.5; 0.8)0.6 (0.0; 1.2)0.7 (0.4; 1.1)
Figure S1. Temporal patterns of air pollution effects in Graz. The title of each graph indicates: cause of death, pollutant (pm.calc. indicating that PM10 was calculated from TSP), pdl (indicating that those are PDL models), and 73/143 (7 and 14 days lags, 3rd degree polynomial). X axis: day, Y axis: change (in%) of daily number of deaths associated with 10 mg/m3 increase.
Figure S1. Temporal patterns of air pollution effects in Graz. The title of each graph indicates: cause of death, pollutant (pm.calc. indicating that PM10 was calculated from TSP), pdl (indicating that those are PDL models), and 73/143 (7 and 14 days lags, 3rd degree polynomial). X axis: day, Y axis: change (in%) of daily number of deaths associated with 10 mg/m3 increase.
Ijerph 10 04728 g004 1024
Int. J. Environ. Res. Public Health EISSN 1660-4601 Published by MDPI AG, Basel, Switzerland RSS E-Mail Table of Contents Alert