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Annals of Forest Science

, Volume 72, Issue 7, pp 887–896 | Cite as

Estimating ozone risks using forest monitoring networks—results for science, policy, and society

  • Antonella CristoforiEmail author
  • Giovanni Bacaro
  • Mauro Confalonieri
  • Fabiana Cristofolini
  • Luisa Frati
  • Francesco Geri
  • Elena Gottardini
  • Gabriele Tonidandel
  • Fabio Zottele
  • Marco Ferretti
Original Paper

Abstract

Key message

Few integration steps (adding low-cost ozone measurements, link to existing conventional monitors, joint data processing) transformed the traditional forest monitoring network into a multifunctional infrastructure producing information relevant for estimating risk to vegetation and human health

Context

Traditionally, forest monitoring networks have been designed to assess status and trends of forest condition. We argue that they can help providing answers to a much broader range of questions for science, policy, and society. Here, we concentrate on the example of ground-level ozone pollution.

Aims

The aim of this study is to demonstrate the value of present forest monitoring networks as infrastructures that—with few integration steps—can provide important data and information to estimate the risk posed by ground-level ozone to vegetation and human health.

Methods

We measured ozone concentration by passive samplers at the local (Trentino, northern Italy) plots of the ICP Forests Level I network over the period 2007–2011. By integrating these data with those from conventional ozone monitors (mostly located in urban areas), we (i) obtained an even distribution of air quality measurements over the investigated area, (ii) estimated international exposure indicators for vegetation and human population, and (iii) obtained data allowing geostatistical modeling and mapping of ozone concentrations, exposure, and associated potential risk.

Results

Mean May–July ozone concentration ranged from 58 to 169 μg m−3, depending on forest site and year. Modeling and mapping (root-mean-square deviation (RMSD) = 12.31 μg m−3) provided evidence that the risk threshold for vegetation in terms of AOT40 was exceeded in large parts (90 %) of the study area, and frequently even by two times, depending on the year. With respect to population, up to 43 % of the dwellers were exposed to medium–high risk of exceedances of the information threshold.

Conclusion

Ozone measurements carried out at the ICP Forests Level I forest monitoring network permitted mapping ozone levels and the estimation of possible risk for vegetation and human health. Forest monitoring networks can be seen as infrastructures that can be useful to address a wide range of environmental issues and with a much broader scope than their original one.

Keywords

Potential risk Directive 2008/50/EC Vegetation Human health Modeling Mapping 

1 Introduction

Tropospheric ozone (O3) originates from photochemical reactions involving primary air pollutants such as nitrogen oxides (NOx, mostly emitted by human activities) and volatile organic compounds (VOC, from both anthropogenic and biogenic emission) (The Royal Society 2008). Ozone has been frequently reported to cause severe risks to a variety of targets, including forest vegetation (Leisner and Ainsworth 2012) and human health (WHO 2000). In Europe, the Directive 2008/50/EC (2008/50/EC 2008) sets acceptable limits for ozone concentration and exposure to protect human health and vegetation, for which thresholds are also defined by UNECE (CLRTAP 2004). These limits provide the basis under which national and regional regulatory agencies operate to identify areas where limits are exceeded and to undertake countermeasures or remedial actions. Information about the amount of the target resource (e.g., population, forests) exposed to potentially harmful ozone concentration over a given region is therefore important to assess the potential risk and “benefit from the provision of high resolution maps” which “are essential for defining the communities most at risk” (Coyle et al. 2002). Such information, however, can be obtained only after an estimation process, which is constrained by the availability of ozone data and/or the prediction ability and applicability of models. This is particularly true when considering remote areas. Here, risk assessment is constrained by three main interrelated aspects: first, measurement of ground-level ozone is possible and/or affordable on a very limited number of sites. Even when available, measured data may have low spatial and/or temporal resolution. Second, it is known that ozone concentration in rural/remote sites is in general higher than those of urban areas, due to lack of chemical scavenging and reduced nighttime ozone depletion (the Royal Society 2008). In contrast, most of conventional monitors are located in urban areas, and—given the above pattern—they generate data that cannot be readily used to infer ozone risk to forests. Third, measured data at individual sites cannot be readily extrapolated over the target region in order to infer a possible risk. These constrains make modeling an important approach for risk assessment. Modeling ambient air quality has a long history (e.g., Kalenderski and Steyn 2011), and ozone photochemical deterministic models have been developed both at large- and local-scale. However, up to now, large-scale deterministic models are typically available with a too coarse spatial resolution (e.g., 50 × 50-km EMEP), not suited for the local-scale risk assessment (EEA 2009). On the other hand, even when developed at the local-scale (e.g., TECHNE Consulting s.r.l. 2006), photochemical models are data intensive and expensive to keep updated. In addition, scientific understanding of the physical and chemical processes may be incomplete for a given region, either in principle or in practice (Kalenderski and Steyn 2011). As a result, statistical and geostatistical modeling can be an option, and several attempts exist in this respect (e.g., Loibl et al. 2004).

Permanent networks of forest-condition monitoring plots have been installed on a systematic basis since the 1980s in Europe (Ferretti and Fischer 2013). They cover remote and forested areas, are georeferenced, and represent a convenient infrastructure for all those information needs that require an even spatial coverage, like the assessment of ozone pollution. Here, we present a study based on 5-year integrated data collection (different sources: passive sampling at forest sites and conventional monitors in urbanized areas), geostatistical modeling and mapping approach to produce “basic” spatial information of ozone data for a montane area in northern Italy, province of Trento (Fig. 1). In this area, ozone is originated in part by precursors from local sources (motorways and urban areas in the valley bottoms) and partly imported during the afternoon by air movements from the nearby heavily urbanized Po valley and Lombardy. A possible contribution of biogenic emission cannot be excluded, although no data was available to estimate its actual importance in the area. The local systematic ICP Forests Level I monitoring network (Lorenz and Fischer 2013) was equipped with passive samplers and integrated with the network of automatic analyzers of the Environmental Protection Agency, Autonomous Province of Trento (APPA). This approach provides the basis (i) to cope with the constrained condition of ozone data availability typical of many montane regions in Europe (e.g., Sanz et al. 2007) and (ii) to functionally connect the higher spatial resolution of the passive sampling network with the higher time resolution of the conventional monitors. The aims were (i) to provide spatially explicit estimates of the risk posed by ozone to vegetation and human health and, by this mean, (ii) to provide a proof of the potential of traditional forest monitoring networks not only for forest science (risk for potential impact of ozone on forests) but also for policy and the society at large extent (risk for seminatural vegetation and human health), demonstrating that multifunctionality of forest monitoring networks can be of great help in reconciling forest monitoring with environmental and societal needs (Ferretti et al. 2013).
Fig. 1

The Italian province of Trento (left) with ozone monitoring sites: passive sampling (triangles) and automatic units (circles)

2 Materials and methods

2.1 Study concept

The passive sampling network was installed in 2007 and was operational up to 2011. It covered forest areas, with passive samplers located in open areas or clearings nearby the plots of the systematic (15 × 18 km) Level I monitoring network, at a mean altitude of 1318 m a.s.l. This network was designed in order to ensure an even coverage of the remote and forest areas (Fig. 1), thus complementing the conventional monitors, which are located in urban/residential environments, at a mean altitude of 213 m a.s.l. (only exception: Monte Gaza, 1601 m a.s.l.). Provided their different nature and time resolution, data from passive sampling and conventional monitors were then integrated and used jointly for (i) geostatistical modeling of ozone concentration and (ii) derivation of consistent indicators for the protection of human population and vegetation. On this basis and with the further integration of temperature data, land use, and census, 1 × 1-km resolution maps were prepared, and percentage of population and vegetation exposed to possible exceedance of threshold values was calculated.

2.2 Study area

The study domain is the Trento province (6207 km2, northern Italy) (Fig. 1), with elevations ranging from the 66 m a.s.l. of the valley bottom (Garda Lake) to the 3769 m a.s.l. of Monte Cevedale. Fifty-five percent of the surface is covered by forests, 27 % by crops and pasture, and only 3 % is urbanized (CORINE Land Cover 2000, retrieved by http://www.eea.europa.eu/themes/landuse/clc-download; access at 1/12/2012). The largest city in the region, Trento, and the main lines of traffic, responsible for most of ozone precursors, are located in the bottom of the Adige Valley. Climate is prevalently humid oceanic-temperate, with cold and dry winters and fresh and rainy summers. Annual precipitation ranges between 800 and 1500 mm, with two maxima in spring and autumn. Annual mean temperature varies between 8 and 12 °C (Eccel and Saibanti 2005).

2.3 Input data for modeling approaches

Input data for modeling included geographical localization and elevation, land use data, spatially explicit modeled temperature data, ozone data from passive sampling and automatic units, and demographic data. Ozone concentration data were collected by eight UV-photometric analyzers with hourly measurement (APPA; n = 7 urban-suburban automatic, n = 1 mountain) and 15–20 sites equipped by diffusive samplers, with weekly exposure time (passam ag, Männedorf, Switzerland; n = 15 in 2007; n = 20 in 2008–2011), exposed in open areas nearby the forest plots for 13 weeks in a period ranging from the end of April to the start of August during the years 2007–2011 (Fig. 1; Online Resource 1). Cross-calibration of passive samplers and automatic analyzers was performed by means of colocated devices (for details see Gottardini et al. 2010).

Weekly mean temperature maps were calculated from hourly temperature maps at a 250-m spatial resolution and then upscaled to the 1-km resolution grid selected for the modeling approach (Gottardini et al. 2010), using the mean value as a linear operator on the pixel values. Maps were modeled by regression-kriging (RK) (Hengl et al. 2007) on hourly mean temperature records from 113 meteorological stations (property of Fondazione Edmund Mach and Meteotrentino).

Based on the data provided by the Statistics Service of the Autonomous Province of Trento, Trentino counted 477,010 dwellers in 2001 and 524,826 in 2010, with a spatial distribution almost unchanged between the two surveys. In particular, the highest population density was found at elevation <500 m a.s.l. Population coverage was estimated for each 1 × 1-km grid cell (the same used for modeling ozone concentration and potential risk) in proportion of the percentage of the surface of each cadastral section falling into the given cell and assuming an homogeneous distribution of the population.

2.4 Geostatistical analysis and modeling

Five annual models were developed, one for each year, 2007–2011 (for details see Online Resource 2). Predictive geostatistical linear models were evaluated to estimate mean ozone concentration in 1 × 1-km grid cells across the entire study domain. Tests for normality and, when necessary, Box-Cox transformation (Legendre and Legendre 1998) were preliminarily conducted on each data series, and subsequently, a generalized linear model was built. Starting from a full model, the final parsimonious, reduced model was identified according to a step-wise procedure, with explanatory variables (elevation and temperatures) chosen through the minimization of the (log) likelihood and the Akaike Information Criterion (AIC) (Cristofori et al. 2012). The low number of included explanatory variables was defined considering the low number of ozone samplers compared to the high number of coefficients to estimate. Cross-validation statistics by leave-one-out procedure was used to assess the bias, and the accuracy of the final spatial model was evaluated by root-mean-square deviation (RMSD). Universal kriging (Krige 1976) was then applied in order to predict mean ozone concentrations in each 1 × 1-km grid cell across the whole Trento province, for the considered period (2007–2011).

2.5 Estimation of potential exceedances of target thresholds for ozone exposure

As for vegetation, ozone accumulated over a threshold of 80 μg m−3 (=40 parts per billion, AOT40) was the indicator defined to evaluate potential risk due to ozone (2008/50/EC 2008; CLRTAP 2004). AOT40 was estimated for each 1 × 1-km cell on the basis of mean concentration data and by a simple linear model (Ferretti et al. 2012a). In order to identify and quantify the vegetation area potentially at risk, the estimated AOT40 was associated to CORINE Land Cover codes for forests (3.1) and seminatural vegetation (3.2). Evaluation was referred to three categories of potential relative risk: AOT40 < risk threshold (RT), RT < AOT40 < 2RT, AOT40 > 2RT. RTs considered in this study were those set by the Directive 2008/50/EC (6000 and 18,000 μg m−3 h−1, long-term objective and target value, respectively) and by UNECE (10,000 μg m−3 h−1, critical level; CLRTAP 2004).

For the population, the information threshold (IT; 180 μg m−3, averaged over 1 h) for human health, set by the Directive 2008/50/EU, was considered, being the most utilized threshold adopted by public agencies to protect sensitive sections of population. The probability P of exceedances of the IT was estimated for each range of 20 μg m−3 of weekly mean ozone concentration, M, as measured by conventional monitors. Weekly M ranges of 20 μg m−3 were compared with the number of weekly exceedances of the IT registered within the same weeks. For each M range, the ratio between the number of weeks with exceedances and the total number of weeks considered returns the P value. The probability is null (P = 0) for values lower than a certain value of M, Mp = 0, and grows with increasing values of M to reach a maximum (P = 1) at Mp = 1. The lower P, the lower the probability to have exceedance of the information threshold and therefore the risk for harmful exposure to ozone. Table 1 reports P values for different M ranges. The probability of exceedances was calculated only for grid cells with elevations <500 m a.s.l. and number of residents >0.
Table 1

Probability of weekly exceedances of the information threshold (180 μg m−3) related to each concentration range (M, μg m−3) at sites equipped with automatic analyzers, mean exceedance probability (±standard deviation) for valley floor only (Monte Gaza excluded) and all sites

Site

M < 60

60 < M < 80

80 < M < 100

100 < M < 120

120 < M < 140

140 < M < 160

Borgo Valsugana

0

0.04

0.44

1.00

Trento Gardolo

0

0.10

Monte Gaza

0

0

0

0.08

0.38

0.50

Trento Parco S. Chiara

0

0.05

0.20

0.60

Piana Rotaliana

0

0.15

0.35

1

Riva del Garda

0

0.05

0.58

1

Rovereto Largo Posta

0

0

0.05

0.56

Grumo S. Michele a/A

0

0.13

0.50

Valley floor

0.0

0.07 (±0.05)

0.35 (±0.20)

0.83 (±0.23)

All sites

0.0

0.06 (±0.05)

0.30 (±0.22)

0.71 (±0.37)

0.38

0.50

2.6 Quality assurance

Data completeness was verified for each automatic analyzer. Mean completeness was 94.9 % (range 60.5–100 %); data series (site/year) with a completeness <90 % were discarded (four out of 31). Reliability of ozone concentration data provided by passive sampling was evaluated by parallel measurements in close proximity of the conventional monitors. Raw hourly mean temperatures used for the modeling were validated using standard data quality routines. Reliability of modeled temperatures was further tested by comparison with data measured by temperature micro-dataloggers (FT-800/System, Econorma s.a.s., Treviso, Italy), positioned in each ozone measurement site.

3 Results

3.1 Ozone concentration

Seasonal and daily time course of mean ozone concentrations recorded by passive samplers and automatic units are reported in Fig. 2. Although the time course is consistent between the two methods, the mean values differ. Besides differing accuracy, this may depend on the location and elevation of the monitoring sites (Gottardini et al. 2010). The well-known pattern for which urban areas (mostly at the valley bottom) show lower ozone concentration than rural/montane areas (mostly at medium to high elevation) (The Royal Society 2008) was proven true also for the Trento Province. Moreover, comparing the daily course of hourly mean ozone concentration for low and high elevation automatic units, a clear reduction of nighttime ozone depletion is demonstrated for the mountain site (Fig. 2).
Fig. 2

Time course of mean ozone concentrations for the considered weeks (left) and for the daytime (right). Mean concentration over 2007–2011 is represented by week for the mountain automatic unit (1601 m a.s.l.), the forest passive sampling sites (n = 15 in 2007, 20 in 2008–2011; mean elevation 1318 m a.s.l.), and the urban-suburban automatic units (n = 7, mean elevation 213 m a.s.l.); bars indicate the standard deviation among years (left). Daily development of the hourly mean of ozone concentration for a mountain and six urban units, referred to 2007 (right)

The basic model features are reported in Table 2. The overall accuracy of the model, as estimated comparing measured and predicted ozone values by RMSD, is relatively high (12.31 μg m−3 against a mean value of 92 μg m−3). Figure 3 reports the comparison between predicted and measured ozone concentration after cross validation. Differences are almost within the expected measurement uncertainty (2013 revision; see http://www.passam.ch/ozone.htm). Predicted 2007–2011 average ozone concentration over the 13 weeks considered is shown in Fig. 4. The maps present the highest ozone concentrations (>140 μg m−3) on the western side of the province, while mean ozone concentrations <100 μg m−3 are estimated for most of the province area. Concentrations are always lower in the valley bottoms and increase with elevation.
Table 2

Description of explanatory variables (and their associated coefficients) included after stepwise selection involved in the reduced spatial model (in bold), built for each year within the study period

Year

Model

Intercept

X

Y

Elevation

T (°)

Spatial parameters

σ 2

φ

τ 2

AIC

2007

Total

2047.773

0.0000

−0.0004

0.0647

5.7128

4.5231

25,348.78

166.0890

191.5/−87.73

Reduced

−35.0896

  

0.0509

4.2651

202.76

28,511.46

133.6205

191.7/−89.83

2008

Total

2330.699

−0.0002

−0.0004

0.0354

2.1798

1.27

2,088,596

117.6

175.9/−79.96

Reduced

38.7184

  

0.0256

1.5598

613.4

44,516

72.31

177.7/−82.87

2009

Total

1891.927

0.0001

−0.0004

0.0781

8.1257

0.0000

0

106.1873

211.1/−97.54

Reduced

−57.0797

  

0.0594

5.5266

319.1

20,712

38.81

211.7/−99.83

2010

Total

3976.102

0.0002

−0.0008

0.0594

5.0465

349.9

6297

11.56

236.2/−110.1

Reduced

−58.0542

  

0.0617

5.6568

846.4

16,252

78.46

239.5/−113.7

2011

Total

3056.203

0.0000

−0.0006

0.0923

9.3345

0

0

294

237.6/−110.8

Reduced

−191.771

  

0.1094

11.8085

724.3

15,542

70.95

236.9/−112.5

σ2 the signal variance, φ range which indicates the distance at which the theoretical variogram reaches its maximum and represents the correlation function parameter, τ2 nugget which represents the intercept of the variogram and determines the conditional or measurement error variance, AIC Akaike Information Criterion, used to estimate model fitting

Fig. 3

Mean ozone concentration (in μg m−3) per site and year (2007–2011). Ozone concentrations predicted by the geostatistical model are plotted against values measured by passive sampling. Solid line represents the bisector (1:1), while dashed lines show the uncertainty of measurement for passive samplers as declared by the manufacturer (20.5 % for an ozone concentration =80 μg m−3; 2013 revision; http://www.passam.ch/ozone.htm)

Fig. 4

Ozone concentrations at 1 × 1-km resolution in Trentino, mean of a 13-week period, 2007–2011

3.2 Potential risk due to ozone

Maps of potential ozone risk for vegetation over the period 2007–2011 and the percent area within each category of relative risk are reported in Fig. 5. All in all, only a small area of vegetation is estimated not at risk (0.17 % in the case of EU long-term threshold; 6.6 % in the case of EU Target value). On the other hand, 93.4–99.8 % of the area with forest and seminatural vegetation appear potentially at risk, with a considerable portion of vegetation exposed to AOT40 values higher than two times the risk threshold (55.0 % in the case of EU Target; 97.8 % in the case of EU long-term).
Fig. 5

Maps of potential risk for vegetation in the Trento province for the period 2007–2011. Risk was estimated considering the target value for 2010 and the long-term objective of Directive 2008/50/EC (18,000 and 6000 μg m−3 h, respectively; top left and right) and the critical level of the UNECE Manual (10,000 μg m−3 h; bottom left). On the bottom right, percentage of forest area for each risk category

Figure 6 illustrates the spatial distribution for the probability of exceedance of the information threshold for human population (180 μg m−3) for all the grid cells below 500 m a.s.l. This elevation limit was set to account for (i) the population distribution pattern and (ii) the probability distribution function that appears to be rather different for high-elevation sites. Exceedance of protection values varies year by year. In detail, between 57 and 92 % of the resident population was exposed to a relatively low risk (<30 %) of exceedance of the information threshold, and between 0.02 and 43 % was exposed to a medium risk (30–60 %). Only one single grid cell presented a high risk of exposure, in 2011, with five residents (0.002 %). Within the study period, the higher percentage of residents exposed to medium or high exceedances was found for the year 2011 (43 %).
Fig. 6

Risk estimates for exceedances of the information threshold for human population (2007–2011): spatial distribution (annual maps) and percentage of population exposed (column chart). Probability of exceedances: null (light blue), low (<30 %, green), medium (>40–60 %, yellow), and high (>60 %, red) (color figure online)

4 Discussion

Estimating the potential risk that ozone poses to natural resources and human health requires concentration data as a basic input for modeling ozone levels across space. Both elements (concentration data and modeling) take advantage of evenly distributed and dense enough measurement networks.

In this paper, we evaluated the feasibility of, and the results obtained by, a modeling approach using available data (ozone and temperature data by existing stations and models, geographical data) and collecting low-cost data at the plots of existing systematic forest monitoring network. Our results show that the geostatistical approach was able to model the mean ozone concentration with a reasonable level of uncertainty. Besides this, results provide concrete evidence of the value of existing forest monitoring infrastructures also when the goal (i.e., assessment of ozone pollution and risk for vegetation and human health) is rather different from their original one (i.e., monitoring forest condition). By means of the forest monitoring network, it was possible to address information needs related to the forest community (exposure to ozone measured at the site; input data for response, correlative studies of ozone impact on growth and health; Ferretti et al. 2012b) and to a larger group of potential data users (input data for modeling and subsequent estimates for e.g., potential risk for human health). In the same line, mapped ozone levels can be of value when ozone impacts on ecosystem services (Mills et al. 2013) are of concern. In a capsule, supplementing the existing plots with passive sampling and ensuring proper integration with other data sources (e.g., conventional monitors, existing temperature models) provided additional value to the original forest monitoring network.

There are, however, several elements that need improvement. From the technical point of view, the probability distribution function of risk threshold exceedance for human health requires to be adapted for high elevation areas. From a more general perspective, adequate communication and dissemination are necessary to make resource managers, decision makers, environmental protection agencies, local health authorities, and monitoring administrators aware of the considerable benefit that few integration steps can provide to the information potential of monitoring networks.

Another issue is the extent at which potential risk can actually result into real effects. Although addressing such an issue is out of the scope of this paper, it is worth mentioning that different factors may modify the actual response to ozone of plants and human beings. This is particularly true for vegetation, for which ozone uptake by foliage (rather than exposure) is considered more suited to evaluate the actual risk (e.g., Reich 1987). Since ozone uptake is controlled by stomatal conductance, actual risk for vegetation can differ from the potential risk inferred by e.g. AOT40 data (The Royal Society 2008). In particular, such a risk can be considerably lower than expected at sites subject to drought condition (e.g. Mediterranean sites). It is worth noting that, due to the local climate, most forests in Trentino experience fresh and rainy summer, with potentially scarce limitation for ozone uptake. Actually, preliminary data showed that time patterns of ozone flux and AOT40 are pretty similar (Ferretti et al. 2012b).

5 Conclusion

Ground-level ozone mean concentration was modeled over a 6207 km2 from data obtained by conventional monitors (mostly in urban areas) and passive sampling in remote sites of already existing forest condition monitoring networks. Cross validation revealed an overall agreement between estimated and measured values, with an estimated root-mean-square deviation (RMSD) of 12.31 μg m−3 against a mean value of 92 μg m−3. Our study provides evidence that Level I monitoring network is an infrastructure that not only can be useful within the forest community but also—with a few integration steps—may serve as a suitable framework to address a wide range of environmental concerns, including human health, even at local level.

We focused on the evaluation of the risks posed by ozone to forest and seminatural vegetation (which are of interest for forest and environmental resource managers) and human health (which is of interest of local health authorities). Based on the forest monitoring grid, we were able to estimate levels and extent of the potential risk, and this is indeed an important step for the environmental management. Whether this potential risk actually results into real effects is out of the scope of this paper and will be subject of further investigation.

The results presented here can be reinforced by more extensive testing at national and international level. This may help in strengthening the concept and improve predictive models. In a time when support for ecological monitoring is becoming increasingly difficult (e.g., Legg and Nagy 2006), demonstrating the multifunctionality of the existing infrastructure may also help in reconciling forest monitoring with environmental and societal needs.

Notes

Acknowledgments

Forests and Fauna Service and Environmental Protection Agency of the Autonomous Province of Trento contributed to the realization of the project, in terms of funding, data sharing, and field work. This is the paper No. 6 originated by the Ozone EFFORT project (Ozone EFFect on FORests in Trentino).

Funding

Funding was from Forests and Fauna Service and Environmental Protection Agency of the Autonomous Province of Trento.

Supplementary material

13595_2014_440_MOESM1_ESM.pdf (14 kb)
ESM 1 (PDF 14.3 kb)
13595_2014_440_MOESM2_ESM.pdf (35 kb)
ESM 2 (PDF 34 kb)

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Copyright information

© INRA and Springer-Verlag France 2014

Authors and Affiliations

  • Antonella Cristofori
    • 1
    Email author
  • Giovanni Bacaro
    • 2
    • 3
    • 4
  • Mauro Confalonieri
    • 5
  • Fabiana Cristofolini
    • 1
  • Luisa Frati
    • 2
  • Francesco Geri
    • 2
  • Elena Gottardini
    • 1
  • Gabriele Tonidandel
    • 6
  • Fabio Zottele
    • 7
  • Marco Ferretti
    • 2
  1. 1.Sustainable Agro-ecosystems and Bioresources Department, Research and Innovation Centre, Fondazione Edmund MachSan Michele all’AdigeItaly
  2. 2.TerraData environmetricsMonterotondo M.moItaly
  3. 3.CNR-IRPI, Istituto di Ricerca per la Protezione IdrogeologicaPerugiaItaly
  4. 4.BIOCONNET, Biodiversity and Conservation Network, Department of Life SciencesUniversity of SienaSienaItaly
  5. 5.Forests and Fauna Service, Autonomous Province of TrentoTrentoItaly
  6. 6.Environmental Protection Agency, Autonomous Province of Trento, Piazza VittoriaTrentoItaly
  7. 7.Geographic Information System, Centre for Technology Transfer, Fondazione Edmund MachSan Michele all’AdigeItaly

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