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iForest - Biogeosciences and Forestry
vol. 8, pp. 95-100
Copyright © 2015 by the Italian Society of Silviculture and Forest Ecology
doi: 10.3832/ifor0799-007

Research Articles

The impacts of a wildfire on hunting demand: a case study of a Mediterranean ecosystem

Konstantinos G Papaspyropoulos (1)Corresponding author, Christos K Sokos (2), Periklis K Birtsas (3)


An increasing interest in the socio-economic aspects related to wildfires is attested by Cortner et al. ([10]), Brunson & Tanaka ([9]) and reviewed by Stokowski ([46]). According to Moreira et al. ([31]) “socio- economic drivers have favored land cover changes contributing to increase fire hazard in the last decades”. The widespread abandonment of traditional land uses during the 20th century has led to the growth of extensive forests, woodlands and scrubs vegetation prone to wildfires, especially in the Mediterranean regions ([4]), contributing also to significant economic losses for the agricultural and livestock production ([29]).

Wildfires are considered as a major disturbance factor to Mediterranean ecosystems, affecting both biodiversity and human activities on forest land ([47]), impacting forest structure and landscape ([19]), causing changes in the taxonomic composition of insect communities ([25]), increasing or reducing populations of some bird and mammal species ([37], [39]), and provoking major impacts on soil gastropods ([8]). Quinn ([36]) discusses the direct and indirect impacts of wildfire to the wildlife. Barlow & Peres ([2]) found a decline in the fruit production and the abundance of species due to wildfires in a central Amazonian forest. On the other hand, Keith & Surrendi ([21]) found more snowshoe hares (Lepus americanus) in burned areas one year after a wildfire. Similarly, an increase in lagomorphs populations after wild or prescribed fires has been reported ([37], [1]). Moreira et al. ([30]) suggest that in Mediterranean ecosystems wildfires can positively affect bird populations, or have little impact on winter visitors like woodcock.

Wildfires also influence human outdoor activities, such as hunting ([50]), which represents an important socioeconomic practice in the Mediterranean area ([28], [43], [44], [45]). About 2.5 million hunters live in areas affected by wildfires in the Mediterranean Europe ([13]). Although in Mediterranean ecosystems hunting is reckoned as an important activity, little information exists in the scientific literature on the impact of wildfires on hunting. In general, researches in recreational economics have focused on the effects of wildfires on the recreation demand ([11], [12], [5]), in particular hiking and biking ([23], [17], [18]).

In Greece hunting has a strong recreational character, and is usually practiced at a local level. However, post-wildfires hunting bans (2-5 years) issued by the Forest Service for wildlife protection may push hunters to move up to 300-500 km in order to find game species ([33], [34]). In Spain, post-wildfires hunting bans last from one to ten years according to Spanish law ([50]).

The goal of the present study is to estimate the impacts of a large wildfire occurred in 2006 in the Kassandra peninsula (north-western Greece) on local hunting activities. Our hypothesis was that hunting activity was negatively affected by the hunting ban issued after the aforementioned wildfire. We investigated the impact of the hunting ban on hunting demand using a socio-economical approach by comparing the following parameters before and after the wildfire: (a) the outdoor activities of hunters in the area; (b) the reduction of hunting licenses after the wildfire; (c) the number of hunting excursions; and (d) the traveling distance of hunters.


Study area

The study was carried out on the Kassandra peninsula of Chalkidiki’s Prefecture, Macedonia (Greece). Kassandra is a touristic and densely populated peninsula and numerous villages or small towns were threatened by the wildfire of August 2006. Total area is 374 km2 and the wildlife refuges where hunting is prohibited cover an area of 57.1 km2.

The study area was a typical Mediterranean landscape with Aleppo pine forests (Pinus halepensis), maquis and cultivated areas (mainly with cereals, legumes and olive groves - [48]). The area was affected by a wildfire on August 21st, 2006, just one day after the opening of the hunting period (Aug 20 - Feb 28). The wildfire burnt an area of 68.7 km2 in the center of the peninsula. Hunting was banned initially on the whole peninsula, then it was restricted to the burned area on Nov 25th, 2006. From the season 2008-2009, the ban was removed and hunting was allowed on the burnt area again.

The main quarry species in the area were hare (Lepus europaeus) and migratory birds: woodcock (Scolopax rusticola), quail (Coturnix coturnix), turtle dove (Streptopelia turtur), woodpigeon (Columba palumbus) and thrushes (Turdus spp.). The hunting period for the hare lasts from September 15 to January 10. Hunting system is “res publica”, i.e., the game become property of the hunter upon payment of an annual license. Furthermore, hunting in the area is allowed to visitors from other hunting clubs with a suitable license (regional or general).

Data collection

Data were collected through structured interviews conducted by telephone on October 2008. This survey methodology is commonly applied in socio-economic researches with the aim of examining citizens’ behavior ([26], [35], [40], [38]).

Licensed hunters of the Kassandra region were in total 512 on October 2008. Only local hunters were interviewed, since they constitute the majority in the region (few non-local hunters usually visit the area). A sample of 56 persons (10.94% of the total) was drawn from the alphabetic catalog of licensed hunters for the period 2008-2009, as provided by the Hunting Club of the Kassandra region. After choosing randomly the first hunter, every fifth person was called next ([14]). If the hunter was not available, the previous or the next one (alternately) in the catalog was called. To avoid biases, consanguinity relations were avoided (e.g., father-son). Similarly to previous researches ([45]), the response rate was 100%.

After a preliminary exploration of the collected data, eleven questionnaires were discarded as respondents were used to practice hunting out of the study area. This resulted in a total of 45 valid questionnaires, a number similar to that reported for analogous studies in the scientific literature ([41], [51]). Variables used for the statistical analysis are reported in Tab. 1.

Tab. 1 - List of variables used in the survey.

Statistical analysis

Data were initially explored by means of descriptive statistics ([6]) in order to obtain some basic information about the sample. Departure from normal distribution of scale variables was verified by the non-parametric Kolmogorov-Smirnov test (α = 0.05). Multiple response analysis ([20]) was used for the analysis of the multiple response variables (see Tab. 1), while for the analysis of hunters’ activities before and after the wildfire, McNemar’s test for paired nominal dichotomous data ([15]) was applied.

Hunters’ behavior before and after the wildfire with regard of their license type was examined through the Marginal Homogeneity test, which is recommended for detecting response changes in categorical variables due to experimental interventions in before-and-after designs ([32]). Furthermore, a two-factor mixed factorial analysis of variance (ANOVA) with repeated measurements was applied ([15]), followed by the post-hoc Bonferroni’s comparison test, in order to reveal possible differences in the number of hunting excursions and in the overall traveling distance before and after the wildfire. Although a non-parametric analysis is more suitable in the case of small sample size, no analogous non-parametric method does exist for the parametric ANOVA mentioned above. Thus, data were prior checked for homogeneity of covariance by the Mauchly’s sphericity test: when such assumption was violated, the Greenhouse- Geisser correction was applied ([15]). All the statistical analyses were performed using the software package IBM SPSS® v.19.0 ([32]) with α = 0.05.

Economic analysis

The economic impact of the wildfire on hunting activities was assessed in two ways. Firstly, according to other environmental economical studies ([7], [24]), the income elasticity of demand for hunting licenses was estimated ([49], [27]) in order to test whether other reasons different from the wildfire (e.g., possible hunters’ income decreases) may have contributed to a possible post-fire decrease in the hunting demand.

Secondly, hunters’ expenditures before the wildfire and for the two subsequent years were compared. As most respondents were local hunters, we expected that the main costs influenced by the post-fire hunting ban were attributable to transportation ([43]), therefore only the vehicle operating costs were considered. Vehicles were divided in two large categories (1: Automobiles; 2: Pickup/Van/Light Trucks - Tab. 2) and their operating costs (in 2007 eurocents km-1) for fuel consumption, maintenance/repairs, tires and depreciation were calculated. Moreover, since the length of the hunting period is different depending on the game species (15 weeks for hares, 25 weeks for birds), the comparison was carried out independently on the following two categories: (i) exclusive hare hunters; (ii) other hunters (including those hunting on hare and other species). The above cost-analysis approach is fairly common in the recreational economics literature ([22]).

Tab. 2 - Vehicle operating costs (2007 eurocents km-1 per vehicle). Source: adapted from Barnes & Langworthy ([3]).

Results and Discussion 

Mean age of respondents was 51.7 years (standard deviation = 15.5, min = 21, max = 79, median = 49), with no significant departure from normality (Kolmogorov-Smirnov 2-tailed test: D = 0.102, p = 0.69). The most preferred quarry species were hare (64.4%), followed by birds, mainly woodcock (42.2 %) and arboreal birds (15.6 %).

Results of the survey carried out in this study are reported in Tab. 3. A significant difference in hunting activity within the burnt area before and after the wildfire was detected (McNemar test for paired nominal data: p<0.05). Indeed, only 6.1% of the respondents went on with hunting after the wildfire of August 2006, while 55% just gave up. Most of the other outdoor activities showed a consistent though non-significant reduction, and some completely disappeared in the post-fire period (e.g., picnicking). Hasanagas et al. ([16]) showed that most human activities on the burnt area were restored two years after the wildfire.

Tab. 3 - Outdoor activities of the respondents in the burnt area before and after wildfire (in %). (a): refers to the beginning of 2008-2009 period, when hunting was permitted in burnt area. (*): p<0.05; (ns): not significant.

Hunting licenses

The mean number of hunting licenses in three hunting periods before the wildfire was 543, and decreased to 470, 495 and 523 for the 2006-2007, 2007-2008 and 2008-2009 hunting seasons, respectively. No statistically significant differences were found between the hunting periods analyzed after the marginal homogeneity (MH) test (Tab. 3). Some 13.6% of the respondents did not renew their hunting license for the 2006-2007 hunting season, and 11.1% acknowledged it as due to the hunting ban. On the other hand, the percentage of respondents with a new hunting license issued for the first time after the wildfire was 4.5%. The fairly low reduction of the number of licenses in the burnt area may be partly explained by the fact that the wildfire occurred one day after the opening of the hunting period, when many respondents had already renewed their license.

Hunting excursions

The total number of excursions before wildfire was estimated at 20 675 per hunting period; after wildfire it decreased to 6 590 for the 2006-2007 hunting season and to 16 697 for the 2007-2008 season. Such reduction was due by: (i) the decrease of the number of hunters; (ii) the shortening of the 2006-2007 hunting period; and (iii) the decrease of the number of excursions per week. Significant differences within-subjects in the variable “excursions per week” were detected after Greenhouse-Geisser test (F[1.7, 59.9] = 4.97, p = 0.014). The interaction between the variable “mean number of excursions” and the factor “direction of residency” was also significant (Greenhouse-Geisser: F[3.4, 59.9] = 3.05, p = 0.03). Significant differences in the mean number of excursions were detected between the 2005-2006 and 2007-2008 hunting periods (mean difference = 0.9, p = 0.007) after Bonferroni tests. Unexpectedly, such difference was not significant for the first period after wildfire (2005-2006 vs. 2006-2007, p = 0.135). This might be due to the shortened hunting period in 2006-2007; thus apparently hunters took more excursions per week to compensate the shortened duration.

The analysis of the interactions among the variables analyzed revealed a significant interaction between the number of excursions and the location (direction) of residency for respondents living south from the burnt area (F = 5.98, p = 0.004 - Fig. 1), likely due to the longer distance from suitable hunting areas.

Fig. 1 - Trend of mean hunting excursions per hunter before and after the wildfire (2006) with regard to the direction of residency from the burnt area.

Travelling distance

The application of the ANOVA to the dependent variable “travelling distance” (TD) did not reveal any significant differences, neither within subjects nor between distance and direction from the burnt area (Mauhly’s W = 0.87, p = 0.18; Fdistance [2, 52] = 0.068, p = 0.93). However, an increase in the traveling distances after the wildfire was observed (TD2005-2006 = 25.4 ± 35.5 km; TD2006-2007 = 40.5 ± 76.8 km; TD2007-2008 = 32.0 ± 49.8 km).

Analysis of income elasticity

Tab. 4 summarizes the main characteristics of the hunting activity for hare and other hunters before the wildfire and in the two subsequent years. From 2005 to 2006 the decrease of hunting licenses was equal to 13.5 %. Considering the Gross Domestic Product per capita for the same period in Greece (17 400 € in 2005, 18 700 € in 2006, and 19 900 € in 2007), the income elasticity of demand (IED) for hunting licenses was calculated. It was reasonably assumed here that hunters (200 000 people, about 2% of the total) are a representative sample of the total Greek population, and that local GDP does not differ from the national one (no GDP data were available for local administrations).

Tab. 4 - Main characteristics of the hunting activity before and after the occurrence of the wildfire in the studied area. (a): Mean average of hunting licenses of the last three years before the wildfire. (HH): hare hunters; (OH): other hunters.

In 2005 and 2006 the IED is below zero for all the categories of hunters (IED05-06→06-07 = -1.8). This means that, contrary to the expectations, the number of hunting licenses issued in the year after the wildfire was lower even though the respondents’ income was higher. Such evidence suggests the hypothesis that the reduction of hunting licenses issued for the burnt area in 2006 was only due the wildfire.

Analysis of car expenses

Tab. 5 shows the total traveling distances of the two categories of hunters with the two class of vehicles considered for the three hunting periods analyzed. Some 81.2% of hare hunters of Kassandra used pick up/van/ light trucks and 18.8% used automobiles, while for the category “other hunters” such percentages were 79.2% and 20.8%, respectively.

Tab. 5 - Total traveling distances in km. (PVLT): Pickup/Van/Light Truck; (A): automobile.

A reduction in the total expenditures (-35 %) was also observed for the first hunting period after the wildfire (Tab. 6) and this is thought to be related to the hunting ban. However, in the second year after the wildfire a large increase in total expenditures (+90.23 %) was observed, which appears to be due to the greater traveling distances as compared with the previous year. The increase of expenditures was lower for hare hunters than for other hunters, as hare hunters are used to hunt closer to their home places ([43], [33]).

Tab. 6 - Total vehicle operating costs per hunter type and per vehicle type (in €). (PVLT): Pickup/Van/Light Truck; (A): automobile.


All outdoor activities in the Kassandra peninsula showed a reduction after the large wildfire occurred in the August 2006 ([5]); however, hunting was found the only activity to be significantly reduced. After the wildfire, a hunting ban was initially issued over the whole Kassandra’s peninsula, then it was limited to the actual burnt area for the subsequent two years. Nonetheless, one year after the wildfire the hare population was higher in burnt area than in nearby non-burnt areas and vegetation regeneration was adequate to provide cover and food to game species ([42]).

The aformentioned hunting restrictions in the studied area had several important socioeconomic consequences. First, a reduction of the number of licenses at the local hunting club was recorded (13.5% and 8.8% for the first and second hunting periods, respectively), even though hunters’ income increased in the same period. The second consequence was the reduction of hunting excursions, especially for hunters living south of burnt area for whom it was difficult to travel out of the banned areas. The third consequence for local hunters was the increase in the traveling distance, mainly in the second hunting period after the wildfire, leading to a strong increase in the vehicle operating costs in the same period (+90.23%). As a result, the lack of hunting areas available in the Kassandra peninsula for the period studied had several impacts like: (i) a higher hunting pressure in allowed areas close to the area interested by the ban; (ii) higher carbon emissions related to the increased distance traveled by hunters ([33]); (iii) relevant economic losses for hunters and local economy. As for the latter point, we calculated that the hunting ban for the period 2007-2008 (one year after wildfire) implied approximately 45 332 € of additional expenses for hunters, mainly due to the operating costs of vehicles. As an alternative, such money could have been recovered (at least in part) through a special license issued for hunting in the burnt areas, and used as a financial support of post-fire management of forest ecosystems and wildlife conservation, such as habitat improvements with proper plantings and wildlife warding.

Our results highlights the lack of integrated managing strategies for areas affected by wildfires in Mediterranean ecosystems. Indeed, the assessments of impacts of wildfires and their consequences (including hunting bans) on local economy should be conducted using an integrated environmental and socio-economic approach and supported by multidisciplinary experts, advisory information and monitoring.


The authors would like to thank the hunters of Kassandra’s Hunting Club and Apostolos Kastoris for his assistance in the data collection.


Amacher AJ, Barrett RH, Stephens SL (2011). Observations of black-tailed jackrabbits (Lepus californicus) increase within forests treated with prescribed fire. The Southwestern Naturalist 56: 117-120.
::CrossRef::Google Scholar::
Barlow J, Peres CA (2006). Effects of single and recurrent wildfires on fruit production and large vertebrate abundance in a central Amazonian forest. Biodiversity and Conservation 15: 985-1012.
::CrossRef::Google Scholar::
Barnes G, Langworthy P (2004). Per mile costs of operating automobiles and trucks. Transportation Research Record 1864: 71-77.
::CrossRef::Google Scholar::
Blondel J, Aronson J (1999). Biology and wildlife of the Mediterranean region. Oxford University Press, Oxford, UK, pp. 350.
::Google Scholar::
Boxall PC, Englin JE (2008). Fire and recreation values in fire-prone forests: exploring an intertemporal amenity function using pooled RP-SP dData. Journal of Agricultural and Resource Economics 33 (1): 19-33.
::Online::Google Scholar::
Bradley T (2007). Essential statistics for economics, business and management. John Wiley and Sons, Chichester, UK, pp. 653.
::Google Scholar::
Branch ER (1993). Short run income elasticity of demand for residential electricity using consumer expenditure survey data. The Energy Journal 4: 111-122.
::Online::Google Scholar::
Bros V, Moreno-Rueda G, Santos X (2011). Does postfire management affect the recovery of Mediterranean communities? The case study of terrestrial gastropods. Forest Ecology and Management 261 (3): 611-619.
::CrossRef::Google Scholar::
Brunson MW, Tanaka J (2011). Economic and social impacts of wildfires and invasive plants in American deserts: lessons from the Great Basin. Rangeland Ecology and Management 64 (5): 463-470.
::CrossRef::Google Scholar::
Cortner HJ, Gardner PD, Taylor JG (2004). Introduction to the special issue: “Humans, fire, and forests: the reemergence of research on human dimensions”. Society and Natural Resources 17 (6): 473-475.
::CrossRef::Google Scholar::
Englin J, Boxall P, Chakraborty K, Watson K (1996). Valuing the impacts of forest fires on backcountry forest recreation. Forest Science 42: 450-455.
::Online::Google Scholar::
Englin J, Loomis J, Gonzalez-Caban A (2001). The dynamic path of recreational values following a forest fire: a comparative analysis of states in the Intermountain West. Canadian Journal of Forest Research 31: 1837-1844.
::CrossRef::Google Scholar::
FACE (2010). Hunters in Europe. Web site.
::Online::Google Scholar::
Garson DG (2012). Sampling. Blue Book Series, Statistical Associates Publishing, pp. 30.
::Online::Google Scholar::
Gray CD, Kinnear PR (2012). IBM SPSS 19 Statistics made simple. Psychology Press, East Sussex, UK, pp. 688.
::Google Scholar::
Hasanagas ND, Styliadis AD, Papadopoulou EI, Birtsas PK (2010). Revcad - Journal of Geodesy and Cadastre 10: 99-112.
::Google Scholar::
Hesseln H, Loomis JB, González-Cabán A, Alexander S (2003). Wildfire effects on hiking and biking demand in New Mexico: a travel cost study. Journal of Environmental Management 69 (4): 359-368.
::CrossRef::Google Scholar::
Hesseln H, Loomis JB, González-Cabán A (2004). Comparing the economic effects of fire on hiking demand in Montana and Colorado. Journal of Forest Economics 10 (1): 21-35.
::CrossRef::Google Scholar::
Hong HS, Mladenoff DJ, Gustafson EJ (2002). Study of landscape change under forest harvesting and climate warming-induced fire disturbance. Forest Ecology and Management 155(1): 257-270.
::CrossRef::Google Scholar::
Jann B (2005). Tabulation of multiple responses. Stata Journal 5 (1): 92-122.
::Online::Google Scholar::
Keith LB, Surrendi DC (1971). Effects of fire on a snowshoe hare population. Journal of Wildlife Management 35: 16-26.
::CrossRef::Google Scholar::
Loomis J, Keske C (2012). Did the great recession reduce visitor spending and willingness to pay for nature-based recreation? Evidence from 2006 and 2009. Contemporary Economic Policy 30 (2): 238-246.
::CrossRef::Google Scholar::
Loomis JB, Gonzalez-Caban A, Englin J (2001). Testing for differential effects of forest fires on hiking and mountain biking demand and benefits. Journal of Agricultural and Resource Economics 26 (2): 508-522.
::Google Scholar::
López PP, Thirlwall AP (2006). Trade liberalization, the income elasticity of demand for imports, and growth in Latin America. Journal of Post Keynesian Economics 29 (1): 41-61.
::CrossRef::Google Scholar::
Mateos E, Santos X, Pujade-Villar J (2011). Taxonomic and functional responses to fire and post-fire management of a mediterranean hymenoptera community. Environmental management 48 (5): 1000-1012.
::CrossRef::Google Scholar::
Maughan B (2004). Investigator-based interviews. International Journal of Market Research 46 (1): 99-102.
::Google Scholar::
McConnell CR, Brue SL, Flynn SM (2011). Macroeconomics: principles, problems, and policies (19th edn). McGraw-Hill/Irwin, New York, pp. 581.
::Google Scholar::
Molina-Martinez J, Vinuela J, Villafuerte R (2002). Reconciling gamebird hunting and biodiversity (REGHAB). Socio-economic aspects of gamebird hunting, hunting bags, and assessment of the status of gamebird populations in REGHAB countries. Part 1. Socioeconomic and cultural aspects of gamebird hunting. REGHAB, London, UK, pp. 52.
::Google Scholar::
Molina-Martínez J, Herrera Machuca M, Zamora Díaz R, Rodríguez y Silva F, González-Cabán A (2011). Economic losses to Iberian swine production from forest fires. Forest Policy and Economics 13 (8): 614-621.
::CrossRef::Google Scholar::
Moreira F, Ferreira PG, Rego FC, Bunting, S (2001). Landscape changes and breeding bird assemblages in northwestern Portugal: the role of fire. Landscape Ecology 16: 175-187.
::Online::Google Scholar::
Moreira F, Viedma O, Arianoutsou M, Curt T, Koutsias N, Rigolot E, Barbati A, Corona P, Vaz P, Xanthopoulos G, Mouillot F, Bilgili E (2011). Landscape - wildfire interactions in southern Europe: implications for landscape management. Journal of Environmental Management 92 (10): 2389-2402.
::CrossRef::Google Scholar::
Norusis MJ (2007). SPSS 16.0 Base. SPSS Inc., Chicago, USA, pp. 527.
::Google Scholar::
Papaspyropoulos KG, Koufis J, Tourlida L, Georgakopoulou A (2012a). Estimating the economic impact of a long-term hunting ban on local businesses in rural areas in Greece: a hypothetical scenario. Animal Biodiversity and Conservation 35 (2): 163-170.
::Online::Google Scholar::
Papaspyropoulos KG, Sokos CK, Hasanagas ND, Birtsas PK (2012b). Sustainability of recreational hunting tourism: a cluster analysis approach for woodcock hunting in Greece. In: “New Trends towards Mediterranean Tourism Sustainability” (Rosalino LM, Silva A, Abreu A eds). NOVA Publishing, New York, USA, pp. 79-94.
::Google Scholar::
Petrosillo I, Zurlini G, Corliano ME, Zaccarelli N, Dadamo M (2007). Tourist perception of recreational environment and management in a marine protected area. Landscape and Urban Planning 79 (1): 29-37.
::CrossRef::Google Scholar::
Quinn R (1994). Animals, fire, and vertebrate herbivory in Californian chaparral and other Mediterranean-type ecosystems. In: “The Role of Fire in Mediterranean-Type Ecosystems” (Moreno JM, Oechel WC eds). Springer-Verlag, New York, USA, pp. 46-78.
::Google Scholar::
Rollan A, Real J (2010). Effect of wildfires and post-fire forest treatments on rabbit abundance. European Journal of Wildlife Research 57(2): 201-209.
::CrossRef::Google Scholar::
Ross-Davis A, Broussard S (2007). A typology of family forest owners in north central Indiana. Northern Journal of Applied Forestry 24 (4): 282-289.
::Google Scholar::
Rost J, Clavero M, Brotons L, Pons P (2012). The effect of postfire salvage logging on bird communities in Mediterranean pine forests: the benefits for declining species. Journal of Applied Ecology 49 (3): 644-651.
::CrossRef::Google Scholar::
Røskaft E, Handel B, Bjerke T, Kaltenborn BP (2007). Human attitudes towards large carnivores in Norway. Wildlife Biology 13: 172-185.
::CrossRef::Google Scholar::
Selin SW, Myers NA (1998). Tourism marketing alliances: member satisfaction and effectiveness attributes of a regional initiative. Journal of Travel and Tourism Marketing 7 (3): 79-94.
::CrossRef::Google Scholar::
Sokos C (2008). Multi-methodical approach for the influence of forest fire on hare (Lepus europaeus) at Kassandra, Chalkidiki, Hellas. MSc dissertation, Department of Forestry and Environmental Management and Natural Resources, Democritus University of Thrace, Komotini, Greece, pp. 76. [in Greek]
::Google Scholar::
Sokos C, Skordas KE, Birtsas PK (2003). Valuation of hunting and management of brown hare (Lepus europaeus) in rangelands. In: Proceedings of “3rd Pan-Hellenic Rangelands Conference - Hellenic Rangelands and Pasture Society”. Karpenissi (Greece) 4-6 Sep 2002, pp. 131-139. [in Greek].
::Online::Google Scholar::
Sokos C, Hasanagas N, Birtsas P (2009a). Compatibility of other species hunting with Wild Boar hunting. In. Proceedings of “7th International Symposium on Wild Boar (Sus scrofa) and on Sub-order Suiformes”. Sopron (Hungary) 28-30 Aug 2008, pp. 104-105.
::Online::Google Scholar::
Sokos C, Hasanagas N, Papaspyropoulos KG, Birtsas P (2009b). Hunting management and hunting - related values. In: Proceedings of “2nd conference on environmental management, engineering, planning and economics (CEMEPE)” (Kungolos A, Aravossis K, Karagiannidis A, Samaras P eds). University of Thessaly and National Technical University of Athens, Greece, pp. 1-4.
::Online::Google Scholar::
Stokowski PA (2007). Human communities and wildfires: a review of research literature and issues. Advances in the Economics of Environmental Resources 6: 165-179.
::CrossRef::Google Scholar::
Thonicke K, Poulter B, Heyder U, Gumpenberger M, Cramer W (2008). Global vegetation-fire pattern under different land use and climate conditions. In: Proceedings of the “AGU Fall Meeting 2008”. San Francisco (CA, USA) 15-19 Dec 2008. American Geophysical Union, Washington, DC, USA, abstract #B42B-02.
::Online::Google Scholar::
Tsitsoni T (1997). Conditions determining natural regeneration after wildfires in the Pinus halepensis (Miller, 1768) forests of Kassandra Peninsula (North Greece). Forest Ecology and Management 92: 199-208.
::CrossRef::Google Scholar::
Wilkie DS, Godoy RA (2001). Tourism marketing alliances: member satisfaction and effectiveness attributes of a regional initiative. Conservation Biology 15 (3): 761-769.
::CrossRef::Google Scholar::
Zamora R, Molina-Martínez JR, Herrera MA, Rodríguez Silva F (2010). A model for wildfire prevention planning in game resources. Ecological Modeling 221: 19-26.
::CrossRef::Google Scholar::
Zhang CZ, Xu HG, Su BT, Ryan C (2009). Visitors’ perceptions of the use of cable cars and lifts in Wulingyuan World Heritage Site, China. Journal of Sustainable Tourism 17 (5): 551-566.
::CrossRef::Google Scholar::


Papaspyropoulos KG, Sokos CK, Birtsas PK (2015).
The impacts of a wildfire on hunting demand: a case study of a Mediterranean ecosystem
iForest - Biogeosciences and Forestry 8: 95-100. - doi: 10.3832/ifor0799-007
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Paper ID# ifor0799-007
Title The impacts of a wildfire on hunting demand: a case study of a Mediterranean ecosystem
Authors Papaspyropoulos KG, Sokos CK, Birtsas PK
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