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Concepts and assessment tools for sustainable natural resource management have been developed in, amongst others, forestry, agriculture, fishery and tourism, but not for hunting or wildlife management. We applied a broad participatory stakeholder approach for the development of criteria and indicators of sustainable hunting in Austria. Based on international and national obligations and provisions, the concept is operational by defining ecological, economic and socio-cultural principles, criteria and sub-criteria with indicators and performance scales. The assessment set enables hunters to assess the degree of sustainability of their own individual practice of hunting in a self-reliant way. Its main function is to serve as a decision-supporting and awareness-raising instrument on hunting to identify deficiencies in sustainability, provide guidance for more sustainable future hunting practices and monitor effectiveness of management actions. The concept allows adaptation to specific regional conditions and different national hunting systems and application on regional and supra-regional scales.
Wildl. Biol. Pract., December 2005, 1(2): 163-183
DOI: 10.2461/wbp.2005.1.20
W. Lexer1*, F. Reimoser2, J. Hackl1, F. Heckl1& M. Forstner3
1Umweltbundesamt Gmbh (Austrian Federal Enviroment Agency Ltd), Vienna, Spittelauer Lände 5, A -
1090 Vienna, A u s t r i a .
* Corresponding author.
(e-mail:; Tel.: +43 1 313-04-3480; Fax: +43 1 313 04-3700)
2Research Institute of Wildlife Ecology, University of Veterinary Medicine, Vienna, Savoyenstraße 1,
A - 1160 Vienna, A u s t r i a .
(e-mail:; Tel.: +43 1 4890915 210; Fax: +43 1 4890915 333)
3WWN – Technical Planning and Consulting Bureau for Wildlife Ecology, Forest Management and
Nature, Neustiftstraße 62, A-3925 Arbesbach, A u s t r i a .
(e-mail:; Tel.: +43 1 2813 7209; Fax: +43 1 2813 7209-4)
I n t ro d u c t i o n
The concept of sustainable use is the leading paradigm of natural resource policy of
the twenty first century. Following the emergence of the model of sustainable
development at the Earth Summit in Rio in 1992 [1,2], generic principles of
sustainable natural resource management have been codified and further elaborated
for sectoral implementations. With regard to biological resources, in particular the
Ecosystem Approach [3,4] under the Convention on Biological Diversity (CBD),
and the recently adopted Addis Ababa Principles and Guidelines for the Sustainable
Use of Biodiversity [5], are powerful concepts that provide major guidance.
Developing operational concepts of sustainable use, however, requires adequate
tools for assessment, monitoring, and adaptive management. For this purpose, the
application of criteria and indicators (C&I) has become a widely recognized
methodical approach. In the course of follow-up processes to Rio and the adoption
of the CBD [6], in many countries and by different international institutions criteria
and indicators for sustainable resource management have been developed for
A b s t r a c t
Concepts and assessment tools for sustainable natural resource management
have been developed in, amongst others, forestry, agriculture, fishery and
tourism, but not for hunting or wildlife management. We applied a broad
participatory stakeholder approach for the development of criteria and
indicators of sustainable hunting in Austria. Based on international and
national obligations and provisions, the concept is operational by defining
ecological, economic and socio-cultural principles, criteria and sub-criteria
with indicators and performance scales. The assessment set enables hunters
to assess the degree of sustainability of their own individual practice of
hunting in a self-reliant way. Its main function is to serve as a decision-
supporting and awareness-raising instrument on hunting to identify
deficiencies in sustainability, provide guidance for more sustainable future
hunting practices and monitor effectiveness of management actions. T h e
concept allows adaptation to specific regional conditions and diff e r e n t
national hunting systems and application on regional and supra-regional
s c a l e s .
game management,
sustainability assessment,
wildlife ecology.
specific applications in various sectors of landuse (e.g., forest management,
agriculture, fishery, tourism). In hunting and wildlife management, however, a lack
of coherent approaches to define and assess sustainable use has existed.
The need for sustainable hunting is reinforced by a number of reasons. Hunting is
a consumptive use of biological resources that is highly environmentally eff e c t i v e
and actively interferes with many ecosystem processes [7]. By preserving and
taking huntable wild living animals, hunting influences genetic diversity and
composition of game species, game populations in terms of size, density,
distribution, structure, dynamics and behaviour, and condition of game habitats.
I n d i r e c t l y , hunting management also exerts impacts on non-huntable animal
species, plant species and ecosystems in general. In particular in European
multiple-use cultural landscapes these impacts often cause conflicts with the
interests of other forms of landuse, such as forestry, agriculture, transport, and
tourism [8]. Moreover, public acceptance of hunting as a legitimate form of landuse
is decreasing [9,10]. In this context, the issue of the sustainability of hunting should
be addressed. While sustainable hunting may be an almost universally accepted
goal, there is, however, no clear understanding of what “sustainable hunting”
exactly means and how it is to be achieved and measured. Therefore, in the course
of a participatory, multi-sectoral stakeholder process for the first time a
comprehensive assessment framework for sustainable hunting has been developed
in Austria [11 , 1 2 ] .
M e t h o d s
O b j e c t i v e s
The main objective of the project was to create a consistent, coherent and
transparent set of principles, criteria, sub-criteria and indicators that would enable
hunters and game managers to assess the degree of sustainability of their own
individual practice of hunting in a self-dependent and user-friendly way.
Conceptual design and indicator set-up have been fitted to the intended key
functions of the assessment set. These main tasks are to function as a decision-
supporting, awareness-raising and educational instrument for hunters to (1)
facilitate analysis and diagnosis of individual strengths and weaknesses in
sustainable hunting, (2) identify sustainability gaps and prior needs for action, (3)
provide guidance in deducing measures for more sustainable future hunting
practices, (4) assess effectiveness of management actions and monitor progress in
the implementation of hunting sustainability, (5) measure changes in levels of
hunting sustainability on the time-scale, and (6) facilitate comparisons of
sustainability performances between different spatial hunting units
(benchmarking). By defining measurable criteria and indicators, the concept of
sustainable hunting shall be made operational. Apart from serving as a tool for
adaptive management, the assessment set shall contribute to the understanding of
"sustainable hunting" by using practice-relevant contents. Creating a common
understanding of "sustainable hunting" shall foster communication with non-
hunters, facilitate reconciliation of conflicts with involved groups of landusers and
create more objective and solution-oriented discussions on hunting-related issues.
External basic conditions
Particular attention has been given to coherence with obligations resulting from
international binding legal sources (conventions, agreements), and “soft law”
regulations, national implementation strategies and relevant political initiatives and
processes. Sustainable hunting is expected to be part of a comprehensive
sustainable development, as stated at the Earth Summit in Rio [1,2] and in the
preceding Brundtland-Report [13], and as further particularised in the course of
subsequent sectoral processes, such as the Ministerial Conference on the Protection
of Forests in Europe (MCPFE), whose Pan-European Criteria, Indicators and
Guidelines for Sustainable Forest Management offer many interfaces with game
management [14-16]. Our approach is explicitly committed to the objectives of the
CBD [6]. In Article 2 of the CBD, "sustainable use" is defined as the "... use of
components of biological diversity in a way and a rate that does not lead to the
long-term decline of biodiversity, thereby maintaining its potential to meet the
needs and aspirations of present and future generations." The Ecosystem
Approach, as the primary frame of action under the CBD, provides operational
principles of integrated ecosystem management that have thoroughly been
considered [3,4]. Recommendations in terms of hunting and wildlife management
contained in the Austrian Biodiversity Strategy [17] have been taken into account.
Our assessment approach is also based on the "Resolution of the IUCN on the
sustainable use of wild living resources" (Amman, 2000), which appreciates that
the consumptive use of wild animals, if it is sustainable, can be an important
conservation tool [18]. However, to determine if a use is sustainable or not,
appropriate assessment criteria are needed.
Within natural resource management a use may be termed sustainable in general
terms if it (1) achieves a proper balance between conservation and sustainable use
of biological resources, (2) obeys the limits of ecological carrying capacity and
ecological functioning of ecosystems, (3) does not exceed the regeneration capacity
of renewable resources, (4) is socially fair and equitable, and (5) preserves an
equivalent resource basis for the needs of future generations [19-21].
Participatory project design and work process
The set-up of the C&I set involved a broad participatory approach that was
gradually extended. It was a multi-sectoral, interdisciplinary, “bottom-up” process
that involved a wide range of stakeholders, experts and practitioners, particularly
representing hunters, science (wildlife ecology, hunting science), forest
management, agriculture, nature conservation, and landowners. In terms of
institutional membership, participants came from organised pressure groups,
NGOs, small and large-scale operations, scientific institutions, authorities, and state
agencies [22]. As a result, the assessment set is based on scientific knowledge and
practice-related expert knowledge, but also reflects the consensus-building process.
In typological terms, the basic conception of our assessment tool may be
characterised as a dynamic, collaborative expert system that is open to updating and
future improvements.
In detail, procedural organisation of the workflow comprised the following
sequential stages (Fig. 1): International and national agreements and initiatives on
the sustainable use of biological resources [e.g.: 3,6,14,15,17,18,23-28],
international standards for designing environmental criteria and indicators sets [29-
45], and principles in terms of hunting ethics, as expressed in the Austrian hunting
laws, were used as a reference frame. Based on preparatory works of the
Umweltbundesamt [7,46], in particular the results of a workshop on "Hunting and
Sustainability" [47], the architectural structure of the assessment set was conceived
by the core project team. Candidate C&I were collected and reviewed, examined as
to their relevance and completeness, supplemented, newly defined and adapted to
the requirements of the large-scale Austrian game habitats. This lead to a first draft
concept version with a preliminary set of C&I, which then was intensely discussed
within expert groups of limited size. Comments and suggestions were harmonised
and worked into a revised concept version. Subsequently, field testings were
Fig. 1. Sequential stages of the participatory work process.
Grey boxes: elaboration of present C&I set (finished); white boxes: intended further
development (in progress).
conducted by applying the assessment set practically in hunting units of varying
size - hunting grounds, “hunting rings” (loose associations of hunting grounds),
small and large-scale operations. The set proved to be suitable for practical
application; some requests for modifications, however, were integrated into the
concept. In parallel, indicator scalings and evaluation schemes were adjusted by
carrying out scenario analyses. At a workshop, an improved draft final report was
then presented to an extended expert audience and discussed in depth within a larg e
panel. Comments, amendments, and requests for changes were to a great extent
integrated into the report. Written statements, which were considered at least
partially in the final report, are documented in full text in the annex of the published
s t u d y. Therewith, each work phase was accompanied by improvements of the
concept. The full final report "Criteria and Indicators of Sustainable Hunting"
[ 1 1,12] has in the meantime also been made available to a broader audience through
an interactive platform in the World Wide Web (http://www. b i o d i v. a t / c h m / j a g d ) .
The website also offers a guided electronic self-assessment by means of an online-
questionnaire. Voluntary feedback of the users is collected and evaluated and will
be used as input for further development [48].
Assessment methodology
The assessment set is structured along two major axis: on the horizontal axis, the
model of "sustainable hunting" is divided into ecological, economic, and socio-
cultural areas of concern, following the common discrimination of "three pillars" of
sustainability [49]. On the vertical axis, within each area the assessment system is
organised as a hierarchical framework that is composed of principles, criteria, sub-
criteria and indicators with performance scales. The set has a tree-like architecture
which - starting from the level of principles at the top and proceeding on down to the
level of sub-criteria - shows a gradually increasing degree of ramification (Fig. 2).
Each principle is specified by a set of criteria, which are again specified by a set of
sub-criteria. Thus, the degree of practical relevancy increases level by level from
top down, while simultaneously the degree of closeness to the model decreases to
the same extent.
Principles describe fundamental objectives derived from the paradigm of
sustainable hunting. They are based on axiomatic value judgements and
characterise a desired ideal state of conditions. Criteria designate certain attributes
of sustainable hunting that are appropriate to define the principles more precisely.
Sub-criteria particularise further selected observable or measurable attributes of the
criteria. Indication and assessment are carried out on the level of the sub-criteria.
Thus, they are required to be particularly practically relevant and meaningful to the
issue of sustainable hunting, representative to the aspect under consideration and
easily verifiable.
Attaching performance scales to each sub-criterion makes them operational and
capable of functioning as indicators (i.e. as measuring parameters which provide
relevant information about the state of the entity that is the object of assessment
[19]). In general terms, the function of indicators is to reduce the complexity of the
real world and improve interpretation by aggregating and simplifying the available
information [50,51]. In a more specific sense used here, the purpose of the
Fig. 2. Exemplification of the hierarchical structure of the assessment framework (detail).
Within each area of sustainability (ecological, economic, socio-cultural aspects), each
principle is specified by a number of criteria, of which each is again particularized by a set of
sub-criteria. Setting ordinal performance scales with a band width of 2 to 4 grades makes sub-
criteria suitable for operational indication. Grades are defined verbally and describe degrees
of fulfilment of a sub-criterion in practice. By assigning points to each grade they are
transformed to numerical scores. Scaling, benchmarking, and implicit weighting of indicators
was done through participatory decision-making.
indicators is to characterise the extent to which a sub-criterion is met by the given
hunting practice. For scaling the indicators, an ordinal performance scale with a
band providing a number of two to four grades per indicator is used. The grades
represent verbal descriptions of degrees of fulfilment of a sub-criterion (i.e. they
describe qualitative states of the indicandum). The grades may also be viewed as a
set of verbalised assessment options from which the user shall choose the one most
fitting. Wherever possible, quantitative parameters are applied to verify fulfilment
of sub-criteria. In case a scale features only two grades, simple yes/no-decisions are
required. Sometimes, however, only assessments based on qualitative information
are possible, depending on the aspect of hunting being assessed.
Numerical transformation of indicators from grades to scores is done by points
which are assigned to each grade on the performance scale [29]. The maximum
range is between + 4 to – 4 points per indicator, scores below zero meaning
“unsustainable”. As the indicator scalings in terms of points are not equal for each
i n d i c a t o r , this implies that an implicit weighting is being applied. However, no
further weighting of indicators is done.
Principles, criteria, and sub-criteria are provided with detailed explanations to give
guidance on their interpretation, to facilitate understanding of their underlying
rationales and to foster critical reflection of the users´ hunting practice.
The application of certain criteria and sub-criteria is dependent on the specific
regional situation or on the spatial scale being assessed and might not be feasible in
any case. Assessing these optional aspects may be omitted, if the reasons are
pointed out adequately. This is taken into account when evaluating the assessment
results (variable maximum/minimum number of points).
Particularly with regard to intolerable forest damage caused by game species the
use of “knock-out” (KO) or “killer criteria”, whose non-compliance would justify
the overall qualification of the practice of hunting as non-sustainable (and whose
compensation in terms of scored points through good results from the assessment
of other criteria would not be possible), is feasible. As the sustainability of
hunting is determined by influences other than hunting (e.g. game damage by
silviculture-related susceptibility of forests to game damage), it was decided to
abstain from mandatory KO criteria for the time being. However, some of those
candidate KO criteria have been weighted heavier than the others by assigning
more points to them. Under special local or regional conditions, nevertheless the
definition of KO-criteria can be useful, provided that adequate justifications are
p r o v i d e d .
Scope of application
The targeted user groups are hunters, hunting managers, and owners of a
p r o p r i e t o r ’s hunt and tenants of a proprietor’s hunt or a co-operative hunt. T h e
assessment refers to the present state of conditions or - where required - to the
preceding calendar year. For some sub-criteria, the required temporal reference
frame may as well extend longer into the past. The intended spatial reference unit
is the hunting ground, hunting operation or a "hunting ring". Moreover, application
to larger assessment units - across hunting grounds - is possible (e.g., by means
of synoptical or comparative evaluation of hunting ground-based assessment results
within a region, an administrative province or a natural landscape unit that is
homogenous in terms of wildlife-ecological conditions). Considering the often
l a rge -scale mobility of many large game species (e.g., red deer [C e rvus elaphus] ,
wild boars [Sus scro f a], brown bears [Ursus arc t o s]) and migratory birds, this can
be very useful.
The assessment methodology and the set of principles are designed in such a way
as to allow general applicability and spatial transferability. Based on the broad
spectrum of Austrian game habitats, ranging from river floodplains to high alpine
regions, the criteria and sub-criteria are particularly attuned to the conditions of
Central European countries with hunting systems based on hunting grounds.
H o w e v e r , by modifying single sub-criteria in an appropriate way, the set can be
adjusted to specific regional conditions and different national hunting systems.
Our mostly qualitative, user-oriented assessment approach is suitable to be fed back
with quantitative results of complementary objective, large-scale monitoring
systems for wildlife species, game populations and game habitats (e.g., network of
representative monitoring areas) [52,53].
The assessment system shall be used voluntarily as a means to support self-
estimation. It was not designed for use as an instrument of governance, legislation
or administration, although the expertise contained therein can be adapted for such
purposes if demanded by future social and political developments [22]. However,
introduction of major contents to teaching aids and education and training
programmes for hunters is a desired application.
Evaluation scheme
Evaluation operates with the number of points scored for each sub-criterion. To
gain clear information on the sustainability of hunting, two types of evaluation are
provided. In a synoptical type of evaluation, the scored points of each individual
sub-criterion/indicator are represented separately and visualised in juxtaposition
using a coloured "sustainability performance scale" (Fig. 3). As no aggregation of
the primary indicators is applied, specific strengths and weaknesses become
visible at a glance on the level closest to practical hunting. A second type of
evaluation uses a simple numerical-additive technique of aggregation up to the
hierarchical level of the three major groups of sustainability aspects (i.e., ecology,
e c o n o m y, socio-cultural aspects). Scores in points within each group are added up,
calculated in percentage of the respective maximum number of points and then
allocated to one of five evaluation classes, which are assigned value rates ranging
from "very good (1)" to "very bad (5)" (Fig. 4). The qualification “very bad” is
given to sums below zero. T h e r e b y, a condensed representation of assessment
results within each major group of sustainability aspects is accomplished, and both
deficiencies and balance with regard to major aspects of sustainable hunting
become evident. The same evaluation procedure may also be applied to individu al
principles or criteria. The concept basically also allows the establishment of p o i n t
limits (minimum requirements) for individual principles or criteria if a j u s t i f i c a t i o n
is given.
Both types of evaluation are intended to be used complementary to provide a
maximum amount of information on sustainable hunting practice.
Fig. 3. Evaluation scheme type 1: Assessment profile of one assessment unit (fictitious
evaluation example, detail; for full coloured figure refer to [11,12,48]).
Assessment results for individual indicators are visualized and represented synoptically.
Column on the left: sub-criteria/indicators; horizontal lines on the right: band width of scales
per indicator; white dots: scored no. of pts. per indicator; figures: scores in pts. per grade;
interpretation: high positive scores (right end of band) indicate good sustainability
performance, low negative scores (left end of band) indicate unsustainable hunting practices.
Fig. 4. Evaluation scheme type 2: Aggregation of assessment results within each major group
of sustainability aspects (fictitious evaluation example; for coloured figure refer to [11 , 1 2 , 4 8 ] ) .
Additive aggregation of scored points, calculation in percentage of maximum number of
points per group, allocation to one of 5 evaluation classes, verbal rating of intervals, coloured
sustainability performance scale with continous transition between sustainable (green) and
unsustainable (red). “Best” and “worst” results for individual indicators are displayed
separately. Maximum and minimum numbers of points are variable to allow for consideration
of omitting of optional indicators.
R e s u l t s
Assessment Set: Technical contents
We defined 11 principles, 20 criteria, and 39 sub-criteria with indicators (Table 1).
In the following section, major contents of the assessment set are briefly outlined.
For complete information, refer to [11 , 1 2 , 4 9 ] .
Table 1. Synopsis of the principles, criteria and sub-criteria of sustainable hunting [11,12].
Cell margins of columns and rows indicate the hierarchical structure of the assessment set.
Positive and negative figures give the possible maximum and minimum number of points per
group of sustainability aspects, per principle, and per criterion, and the band width of indicator
scalings respectively. Column “No” … sequential numbers of sub-criteria; X… optional sub-
criteria (assessment may be omitted, if justification is given).
(Pts. max./min.)
(Pts. max./min.) No SUB-CRITERION
Range of
max. min.
Ecology 48 -21
The practice of hunting
shall within its range
ensure the conservation
and improvement of the
diversity of game species
through protection and use
Potential natural wildlife
species inventory taking into
account the current habitat
situation (applies only to larger
territorial units, e.g. a wildlife-
ecologically homogeneous area
or a Province) (6/-3)
1Current and potential list of wildlife species 2 0
Dealing with newly appearing species (in
accordance with the potential wildlife species
X 2 -1
3Dealing with wildlife species not contained in the
potential wildlife species inventory X 2 -2
Hunting is oriented according
to the behaviour of wildlife
species (9/-3)
4Giving consideration to the undisturbed life cycle of
wildlife species 2 -1
5Considering the reproductive periods of the
individual game species 3 0
6Existence of hunting guidelines across hunting
grounds 4 -2
The conservation and
improvement of wildlife
habitats is an objective of
the practice of hunting
Hunting and its
interrelationship with other
forms of land use (10/-4)
7Existence of a strategy to coordinate hunting with
other forms of land use 2 0
8Considering seasonal bottleneck situations in food
supplies 2 -2
9 Existence of a shooting plan and a shooting list 3 -1
10 Structure of shooting plan and shooting list 3 -1
Giving consideration to the
impact of game on vegetation
11 Existence of control fences to monitor browsing X 2 0
12 Giving consideration to the results of objective
forest monitoring systems X 2 0
13 Giving consideration to the protective function of
the forest X 2 0
14 Preventing game damage that is unacceptable
particularly in terms of public interest 0 -4
15 Giving consideration to population fluctuations 2 -2
Conservation and promotion
of biotope connectivity (4/-2)
16 Giving consideration to existing wildlife habitat
fragmentation X 2 -1
17 Increasing the attractiveness of important wildlife
corridors and obligatory wildlife passages X 2 -1
Giving consideration to habitat
capacity (6/-2)
18 Completeness of the wildlife habitat 2 -1
19 Giving consideration to competitive relationships
of various wildlife species 2 -1
20 Extent of annual growth rate in ungulates 2 0
Table 1. (cont.)
(Pts. max./min.)
(Pts. max./min.) No SUB-CRITERION
Range of
max min.
The natural genetic
diversity of game species
is conserved and fostered
by means of an appropriate
hunting practice (5/-1)
There are no hunting-related
limitations to the conservation
and fostering of the natural
genetic variability of game
species (4/0)
Existence of aims relating to the aesthetics of
trophies (forms of horns and antlers) in shooting
2 0
22 Selective hunting of wildlife according to certain
natural characteristics of individuals 2 0
Native wildlife populations are
not altered by the introduction
of and blending with exotic (not
native, alien) wildlife (1/-1)
23 Introduction of exotic (not native, alien) wildlife 1 -1
Economy 26 -9
Securing and/or improving
the economic profitability
of hunting is an objective
of hunting (8/-3)
The profitability of hunting is
secured over a medium term
24 Existence of a marketing strategy 2 0
25 Expense/yield ratio 2 -1
26 Marketing of game X 2 -1
The value of hunting is
maintained and/or fostered by
the practice of hunting (2/-1)
27 Hunting-related measures to increase the market
value X 2 -1
Preserving and fostering
the condition of the game
is an objective of hunting
Average game weight (5/-1) 28 Continuous, long-term comparison of game
weights 3 0
29 How high is the game weight? 2 -1
Existence of a time- and area-
specific hunting strategy (3/0) 30
Existence of an economically sound hunting
strategy for the temporal and spatial
implementation of hunting, documentation of the
planning, practice and evaluation of hunting
3 0
Preventing damage to
agriculture and forestry is
an objective of hunting
Hunting is oriented according
to the susceptibility of
agricultural land and managed
forests to game damage (4/-2)
31 Giving consideration to game damage
susceptibility 4 -2
Making use of synergies
with other economic
branches is an objective of
hunting (6/-3)
Hunting forms an economic
unit with other foreseeable
anthropogenic forms of land
use (2/-1)
32 Confirming a common policy 2 -1
Optimising planned changes in
wildlife habitats by way of
interdisciplinary spatial
planning (4/-2)
33 Interdisciplinary wildlife-ecological spatial
planning (WESP) 4 -2
Socio-cultural aspects 11 -9
The use interests of the
local population in hunting
are taken into account (3/0)
Hunting establishes balanced
relationships to the local
population through an
appropriate involvement of
local hunters (3/0)
Reconciling the interests of local hunters permitted
to hunt locally and local hunters not permitted to
hunt locally
3 0
Securing local jobs in the
field of hunting is to be an
objective (2/-1)
Hunting contributes to
securing employment by
providing job opportunities
35 Providing jobs in the field of hunting 2 -1
Hunting should find broad
acceptance among the local
population (2/-2)
Giving consideration to the
interests of the local
population (2/-2)
36 Documentation of disagreements at the local
authority 2 -2
Hunting is oriented
according to the well-being
of the game (4/-6)
Hunting is practised with as
little adverse effects on the
natural behaviour of wildlife
as possible (2/-2)
37 The behaviour of wildlife shows that it feels safe
and undisturbed by hunting activities 2 -2
Hunting causes as little pain
for animals as possible (2/-4)
38 Violations of legal regulations regarding animal
protection 0 -4
39 Training in shooting 2 0
E c o l o g y
As far as ecological aspects are concerned, the P, C and I are oriented on the
conservation and improvement of game species diversity, genetic diversity of game
species and diversity of game habitats. Particular importance is attached to the handling
of potentially natural game species (present, returning, extinct species) and non-
autochthonous species. The amount of consideration that is given to the undisturbed life
cycle of wildlife species, to critical factors of the reproductive biology of sensitive
species and to the large-scale mobility of game species across hunting grounds indicates
whether hunting is oriented according to the behaviour of wildlife species.
Other indicators deal with interactions of hunting with other forms of land use (e.g.,
agriculture, forestry), which requires an adequate strategy that should be established in
a hunting concept. Hunting strategies should consider the seasonal fluctuations in food
supplies of wildlife. Shooting plans and shooting lists are an absolute requirement for
planning and documenting hunting activities because they are crucial instruments for
the regulation of game stocks.
Considering the impact of game on vegetation is highly important [54]. Browsing
control fences and forest monitoring systems are considered to be useful instruments to
control game impacts by browsing. When assessing ecological sustainability,
preventing unacceptable game damage is of particular significance, especially with
regard to the protective function of forests. Tolerating temporary natural population
fluctuations of abundant ungulate game species below average levels is another
indicator related to this issue.
The last few decades have seen an increase in habitat alteration and fragmentation,
which was caused mainly by agricultural landscapes poor in structural diversity and by
high-ranking transportation infrastructure. It is therefore assessed whether the
possibilities for linking biotopes are exhausted and whether migration zones and
wildlife corridors are taken into account by hunting. Furthermore, the varying habitat
capacity for game populations has to be considered [7]. By considering habitat
improvement measures, hunting is able to contribute to meeting the habitat
requirements of wildlife. Competitive relationships of various species should be given
consideration to by hunting (e.g., by regulating increasing populations of game species
that are threatening the viability of other wildlife species directly or indirectly). T h e
extent of annual growth rate in ungulates may indicate whether the density of game
populations is adapted to habitat capacity.
The impact of hunting on the genetic diversity of game species is indicated by assessing
whether shooting guidelines are oriented on aims relating to the aesthetics of trophies
(i.e., forms of horns and antlers), and whether shooting is carried out in a selective way
(e.g., according to idealised (unrealistic) images of trophies, preferred shooting of male
individuals or of individuals with certain natural behaviour patterns). Moreover, the
introduction of exotic game species contributes to alteration of the natural gene pool.
E c o n o m y
Securing the capability of yielding returns and the profitability of hunting is a major
objective of economically sustainable hunting [55]. Accomplishment of this objective
is, for instance, indicated by the existence of a marketing strategy for game, bags,
shootings, and trophies, by the monetary expense-yield ratio of a hunting operation, and
by the amount of proceeds from game. Also, for tenants and owners of proprietor’s
hunts, hunting-related measures to increase the market value of a hunt are evaluated,
such as investments in installations and equipment on the hunting ground. Long-term
documentation of game weights is used as an indicator for the yield and economic value
of hunting; it can also provide some evidence on the condition of the game, which in
turn can to some extent be influenced by hunting strategies [56]. An economically
sound, spatial and temporal hunting strategy is crucial for the efficiency of hunting and
therefore should be continuously documented in a written hunting concept.
Orientation of the practice of hunting on the susceptibility of agricultural crops and
forest stands to damage by game is an important attribute of economically sustainable
hunting. This requires organizing hunting activities with other land use sectors and their
representatives on a regular and mutual basis. Hunters are able to optimise both
s y n e r gies with other economic branches and interferences in wildlife habitats by
actively supporting wildlife ecological spatial planning (legally binding or applied
voluntarily on a regional scale) [57]. Such commitment is therefore considered as a
contribution to the sustainability of hunting.
Socio-cultural aspects
Indicators of socio-cultural aspects refer to the relationships among hunters and
between hunters and non-hunters, and to ethical issues.
Reconciliation of interests between local hunters permitted to hunt locally and those
who are not indicates the extent to which the hunting interests of the local population
are considered. Disagreements documented at the local authority provide clues as to
whether the interests of the non-hunting local population, particularly those of land
owners, land users and their representatives, are taken account of, which is seen as a
valuable contribution to safeguarding sustained social acceptance of hunting.
Contributions of hunting to securing local jobs are used as another indicator.
Sustainable hunting must comply with the requirements of modern animal protection.
Hunting must be carried out in such a way as to ensure that the pain caused to the hunted
game is as little as possible. Here, appropriate and regular training in shooting and
compliance with animal welfare laws are demanded. If the behaviour of game shows
that it feels safe and undisturbed by hunting activities, this is regarded as an important
indicator of its well-being.
D i s c u s s i o n
Participatory process
For the process set-up, no particular socio-scientific model, but a flexible, case-based
approach was applied. While various forms of participation may not be new to conflict
management in environmental planning and natural resource affairs, no similar nation-
wide multi-stakeholder process in relation to hunting issues is known in Europe.
Responding to increasing international demands for participatory indicator
development [2,3,4], our basic idea was to establish an organisational framework that
fosters collaborative learning and acceptance of the project outcome by the targ e t e d
users. We assumed that acceptance is facilitated by active personal involvement in the
decision-making process and is, in turn, the pre-condition for commitment to
implementation of jointly elaborated results [58]. Involving the accountable social
actors directly from the beginning was also based on the conviction that hunting and
wildlife management in the end is to a greater extent a human problem than a
biological one, and that managing people is much more effective than managing the
animals [59,60,61].
All stages of the participation process brought about modifications and improvements
of the study without, however, fundamentally altering the substance of the draft
version agreed upon in the first expert group discussion. Also, the basic structure of the
assessment set and the assessment methodology remained virtually unchanged. W h e n
b a rgaining trade-offs, the core project team was flexible about the wordings, while
remaining firm about substantial contents. Further changes focused on scalings, scores
and weighting of indicators.
Assessment Methodology
Among the C&I sets studied, the conceptual framework of CIFOR for sustainable
forest management [29,31] and two topical workshops held by the Umweltbundesamt
[32,47] provided guidance for our project. The development of indicators usually faces
the so-called “pyramid dilemma”. Top-down approaches that attempt to infer
indicators from the generic model often lack problem-adequacy, whereas problem-
oriented bottom-up approaches that try to condensate indicators by aggregating
available data may lack coherency with the questions being asked [50,62]. To bypass
this dilemma, we chose a more flexible, dual approach by practising a mix of both
techniques. The construction of the assessment framework was based on a scoping of
existent practical problems, while simultaneously orienting on superior principles of
sustainable hunting [19,50]. No particular theoretical model was used to derive our
indicator set.
"B a s i c a l l y, everything is an indicator of something but nothing is an indicator of
e v e ry t h i n g" [63]. This statement shows that the selection of indicators and the
identification of attributes suitable for verification is a difficult and critical step.
Indicators are tools that determine the image we construct about our environment. T h e
choice of indicators determines what is being assessed and affects the quality of
assessment results [64].
Apart from standard methodical criteria [62,65], indicator selection is heavily
dependent on the intended purpose of assessment and the targeted user group [62]. Our
assessment set directly appeals to hunters and is aimed at influencing practical hunting
b e h a v i o u r . Thus, indicators were required to be representative and relevant to hunting-
related problems and meaningful in terms of sustainable hunting [19]. Moreover, in
particular pragmatic, user-oriented selection criteria were essential to meet the specific
practice-related requirements: simplicity, practicability, easy applicability and user-
friendliness, clearness and time-efficient verification.
This has implications for data requirements: indicators must be applicable without a
l a rge amount of quantitative data, additional data collections, or in-depth
investigations. Instead, data input for assessment must largely rely on the information
that can be expected to be readily available within the individual hunting ground, and
on instant "soft" expert knowledge based on experience.
B a s i c a l l y, each indicator approach represents a trade-off between scientific accuracy
and both practicability and usefulness [65]. Not everything that can be observed can
easily be measured [39]. Moreover, observable attributes often do not have to be
measured to provide useful information. For us, it was essential to include qualitative,
b e h a v i o u r -related attributes of hunting in the C&I-set. Focussing exclusively on
information that can easily be quantified would have unnecessarily narrowed our
perception of reality and reduced the set’s force of expression [65]. This implies that
verification of some sub-criteria may demand a certain amount of discretionary
decision on the part of the users. However, one must remember that this is a self-reliant
approach meant to support self-assessment, whose emphasis is on changing cognitive
and behavioural patterns related to hunting, rather than on accurate "measuring" of
hunting sustainability in quantitative terms.
Since participatory indicator development grants legitimization by stakeholders,
scaling and benchmarking of indicators could be done in a collaborative manner,
which warrants inter-subjectivity. To some extent, the implicit weighting of the
indicators (i.e., range of points, no. of points per grade) is therefore connected to
value-based decisions of the participants that, however, reflect the consensus-
building process. Still, as the scores in points are laid open via the performance
scales, the accomplishment of the assessment results is transparent and reproducible
Evaluation scheme
Aggregation of indicator performances by means of simple mathematical summation
of scored points, as applied in evaluation type 2 (Fig. 4), is an often used technique to
condense information [29,31,34]. This may lead to the concealing of
interdependencies and of overlaps between individual indicators [67]. But for the
pragmatic purpose of supporting a quick and rough assessment of the extent to which
the three major areas of sustainability are affected by strengths and weaknesses, this
objection is negligible (e.g. hunters might want to know if they are "better" in the
ecological or economic area). However, no further aggregation beyond the level of
ecological, economic, socio-cultural groups of aspects is performed, because
producing one single "sustainability value" would only reduce the value of
information. Also, except adding up scores in points and relating them to the maximum
number of points of each group, no other calculations and no mathematical algorithms
are applied, since this would reduce transparency of the evaluation scheme and might
be questionable in methodological terms due to the use of ordinal indicator scalings
[57]. Possible loss of information in consequence of aggregation is avoided by
providing the evaluation type 1 (Fig. 3), which presents the scores of all individual
analytical indicators in overview. It provides a complete assessment profile of the
assessment unit under investigation. In a similar way, for comparative assessment of
d i fferent hunting grounds, indicator profiles displaying all results of one indicator for
each assessment unit can be produced. Complementary use of both evaluation schemes
allows swift identification of strengths and weaknesses regarding sustainability
performance and facilitates interpretation. Using coloured graphical “sustainability
performance scales” increases the clearness of representation.
The issue of feeding is not dealt with directly in the assessment system because it can
have very diverse impacts on the indicators and thus is difficult to assess as to its
e f fects in terms of sustainable hunting. Depending on how and on which location it is
carried out, feeding may reduce game damage (e.g. of forests), but it may also cause
such damage. Where natural winter habitats, e.g. for red deer, are not available
anymore (due to anthropogenic influences), feeding may represent a technical
“remedy” for the lost habitat, which allows a sustainable use of the respective animal
species [68]. If feeding contributes in a positive sense to a better fulfilment of the
sustainability criteria, it is automatically positively entered into the assessment.
Negative impacts of feeding on sustainability are sufficiently reflected in the existing
sustainability criteria.
Interpretation of assessment results
The concept is deliberately weighted towards ecological sustainability, because the
integrity and functional capability of the ecological system determines the potential for
sustainable development of the social and economic human sub-systems [20,69]. T h i s
is reflected by the higher number of sub-criteria and the higher number of maximum
and lower number of minimum scores in the ecological area. This implies that the class
widths of the evaluation classes (evaluation scheme 2; Fig. 4) are larger in the
ecological area compared to the economic and socio-cultural areas, which particularly
applies to the class "very bad". Thus, good evaluation results in terms of ecologic
sustainability may be more difficult to achieve.
Certain indicators from different areas of sustainability may be controversial to each
o t h e r . Also, the same sub-criterion may be assessed differently from the perspective of
d i fferent areas. During the assessment process, it therefore is important to always be
aware of the area a certain sub-criterion belongs to, to avoid, for instance, an intuitive
incline towards economic judgement when assessing an ecological sub-criterion (and
r e c i p r o c a l l y ) .
L i m i t a t i o n s
This is a hunting-specific C&I-set. The influences of hunting on animal species that
are not hunted are not explicitly covered by our approach. Also, the manifold impacts
from other land uses on wildlife, wildlife habitats and hunting management which
often superimpose influences exerted by hunting itself and restrict its scope for action
[8] are not subject of our assessment system. Only actions of hunting itself that may
contribute to optimising interrelations with other economic sectors are assessed.
Nevertheless, it intendedly offers interfaces towards other forms of land use; it
therefore can be integrated into future cross-sectoral sustainability concepts.
As is inherent in any self-assessment, a source of constraint lies in a certain scope of
subjective interpretation some sub-criteria leave to the user. A certain amount of honesty
and ability for self-criticism is required and must be expected from the users.
Due to difficulties in defining verifiable sub-criteria, the present version of the
assessment set may lack socio-cultural indicators dealing with aspects of hunting
tradition and hunting culture in the narrower sense. This gap shall be closed in the future.
A c k n o w l e d g e m e n t s
The project has been conducted by the Umweltbundesamt GmbH (Austrian Federal Environment
Agency Ltd), the Research Institute of Wildlife Ecology at the University of Veterinary Medicine
Vienna, and the Technical Consulting and Planning Bureau DI Martin Forstner – WNN. The study has
been financially supported by the Austrian Federal Ministry of Agriculture, Forestry, Environment and
Water Management (Lebensministerium) and translated with support by FUST A c h e n k i r c h / T yrol. T h e
authors wish to express thanks to all who participated in the development.
R e f e re n c e s
1. UNCED (United Nations Commission on Environment and Development) 1992. The Rio declaration
of environment and development. UN General Assembly, document A/CONF.151/26 (Vol. I). Cited 26 Jul 2004.
2. UNCED (United Nations Commission on Environment and Development) 1992. Agenda 21: Global
programme of action for sustainable development. Cited 26 Jul 2004.
3. UNEP/CBD/COP/5/ decision V/6 2000. Decision V/6 of the Conference of the Parties to the
Convention on biological Diversity, 5th meeting, Nairobi, Kenia, May 2000: Ecosystem Approach.
In: UNEP/CBD/COP/5/23 2004. Cited 26 Jul 2004.
4. UNEP/CBD/COP/7/decision VII/11 2004. Decision VII/11 of the Conference of the Parties to the
Convention on biological Diversity, 7th meeting, Kuala Lumpur, Malaysia, 9-20 Feb 2004:
Ecosystem Approach. In: UNEP CBD/COP/7/21 2004. Cited 26 Jul 2004.
5. UNEP/CBD/COP/7/decision VII/12 2004. Decision VII/12 of the Conference of the Parties to the
Convention on biological Diversity, 7th meeting, Kuala Lumpur, Malaysia, 9-20 Feb 2004:
Sustainable Use (Article 10). In: UNEP/CBD/COP/7/21 2004. Cited 26 Jul 2004.
6. CBD (1992) Convention on biological Diversity. Cited 26 Jul 2004.
7. Zeiler, H. 1996. Jagd und Nachhaltigkeit. (Hunting and Sustainability). Monographs of the
Umweltbundesamt M-73. Umweltbundesamt, Vienna.
8. Reimoser, F. 1987. Umweltveränderungen in Österreich, ihr Einfluss auf die Populationsentwicklung
jagdbarer Wildtierarten und Konsequenzen für eine ökologisch orientierte Landeskultur.
(Environmental changes in Austria, their impact on population development of huntable wildlife
species, and consequences for an ecologically oriented provincial culture). Verhandlungen der
Gesellschaft für Ökologie (Graz 1985), Bd. XV 1987: 129-144.
9. Myrberget, S. 1990. Wildlife Management in Europe outside the Soviet Union. Norwegia Institut of
Nature Research NINA Tungasletta 2. Trondheim.
10. Braunegger, E. 1994. Jagd und Öffentlichkeit. In: `Überlebt die Jagd`? Symposium der Steirischen
Landesjägerschaft am 18.11.1994 in Stift Vorau. (Hunting and the public. In: “Will hunting survive”?
Symposium of the Styrian hunting association on 18/11/1994 in Stift Vorau).
11. Forstner, M., Reimoser, F., Hackl, J. & Heckl, F. 2001. Kriterien und Indikatoren einer nachhaltigen
Jagd. (Criteria and Indicators of sustainable Hunting). Monographs of the Umweltbundesamt M-158.
Umweltbundesamt, Vienna.
12. F o r s t n e r, M., Reimoser, F., Hackl, J. & Heckl, F. 2003. Criteria and Indicators of sustainable Hunting.
Monographs of the Umweltbundesamt No. 158. English translation of M-158. Umweltbundesamt, Vi e n n a . Cited 26 Jul 2004.
13. Brundtland, G.H. & UNCED (United Nations Commission on Environment and Development) 1988.
Our common future. Oxford University Press, Oxford.
14. MCPFE (Ministerial Conference on the Protection of Forests in Europe) 1993. Decisions and
resolutions of the Second Ministerial Conference on the Protection of Forests in Europe, 16-17 Jun
1993, Helsinki/Finland. Conference Proceedings.
15. MCPFE (Ministerial Conference on the Protection of Forests in Europe) 1998. Decisions and
resolutions of the Third Ministerial Conference on the Protection of Forests in Europe, 2-4 June 1998,
Lisbon/Portugal. Conference Proceedings.
16. MCPFE (Ministerial Conference on the Protection of Forests in Europe) 2002. Improved pan-
European indicators for sustainable forest management. MCPFE expert level meeting, 7-8 Oct 2002,
Vienna/Austria. MCPFE Liason Unit, Vienna.
17. BMUJF (Federal Ministry of Environment, Youth and Family A ffairs) 19 98. A u s t r i a n
Implementation Strategy for the Convention on biological Diversity. Series of the BMUJF Vol.
31/1998. BMUJF, Vienna.
18. IUCN (The World Conservation Union) 2000. The IUCN Policy Statement on sustainable Use of wild
living Resources (resolution 2.29). Adopted at the IUCN World Congress, Amman/Jordan, Oct 2000. Cited 26 Jul 2004.
19. SRU (Rat von Sachverständigen für Umweltfragen) 1994. Umweltgutachten 1994. Für eine
dauerhaft-umweltgerechte Entwicklung. (Environmental Experts Report 1994. For a sustainable
development. Stuttgart, 1994).
20. B.U.N.D. & MISEREOR 1997. Zukunftsfähiges Deutschland: ein Beitrag zu einer global
nachhaltigen Entwicklung. Studie des Wuppertal Instituts für Klima, Umwelt und Energ i e .
(Sustainable Germany: a contribution for a globally sustainable development. Study of the Wuppertal
Institute for Climate, Environment and Energy). Birkhäuser, Berlin.
21. Kosz, M. 1994. Action Plan Sustainable Austria. Auf dem Weg zu einer nachhaltigen Entwicklung in
Österreich. (Action Plan Sustainable Austria. On the Track towards a sustainable development in
Austria). Nestelbach, Wien.
22. Lexer, W., Forstner, M., Reimoser, F., Hackl, J. & Heckl, F. 2003. Wie nachhaltig jagen wir? (How
sustainable do we hunt?)Die Pirsch 5: 4-11.
23. CMS 1983. Convention on Migratory Species (“Bonn Convention”). 23 Jun 1979, Bonn.
24. European Council (1996) Pan-European Biological and Landscape Diversity Strategy (PEBLDS).
EC/UNEP/European Centre for Nature Conservation, Amsterdam.
Available via
25. European Council 1979a. Convention on the Conservation of European Wildlife and natural Habitats
(“Bern Convention”). 19 Sept 1979, Bern. Available via
26. European Council 1979a. Council Directive 79/409/EEC of 2 April 1979 on the Conservation of wild
Birds (“Birds directive”).
Available via
27. European Council 1992. Council Directive 92/43/EEC of 21 Mai 1992 on the Conservation of natural
Habitats and of wild Fauna and Flora (“Flora-Fauna-Habitat-directive”).
Available via
28. BMU (Federal Ministry of the Environment) 1995. National Environmental Plan. Austrian Federal
Government, Vienna.
29. CIFOR (Center for International Forestry Research) 1999. Guidelines for developing, testing and
selecting Criteria and Indicators for sustainable Forest Management. C&I toolbox series no. 1.
CIFOR, Jakarta.
30. CIFOR (Center for International Forestry Research) 1999. The CIFOR Criteria and Indicators
generic Template. C&I toolbox series no. 2. CIFOR, Jakarta.
31. Umweltbundesamt 1996. Testing of Criteria and Indicators of sustainable Forest Management within
the international CIFOR Project. Special edition. Umweltbundesamt, Vienna.
32. Umweltbundesamt 1999. Umweltindikatoren für Österreich. Regionale und nationale Maßzahlen zur
Dokumentation der Umweltsituation auf dem Weg zu eine r nachhaltigen Entwicklung.
(Environmental Indicators for Austria. Regional and national measuring Parameters for the
Documentation of the environmental Situation on the way towards a sustainable Development).
Workshop 16-17 Nov, 1998, Vienna. Conference Papers Vol. 26. Umweltbundesamt, Vienna.
33. FSC (Forest Stewardship Council) 2000. FSC Principles and Criteria. Document 1.2. Revised Feb
Available via Cited Jan 2003.
34. WWF (World Wide Fund for Nature) 1998. European Forest Scorecards 1998.
35. PEFC (Pan European Forest Certification) 1999. Österreichischer Katalog von Kriterien und
Indikatoren zur Messung der Nachhaltigkeit der Waldbewirtschaftung in Österreich. Appendix 1.
(Austrian Catalogue of Criteria and Indicators for the Measurement of the Sustainability of Forest
Management in Austria. Appendix 1).
h t t p : / / w w w. p e f c . a t / d o w n l o a d / k r i t e r i e n _ u n d _ i n d i k a t o r e n _ n a c h h a l t i g e _ w a l d b e w i r t s c h a f t u n g . p d f .
Cited 26 Jul 2004.
36. Rametsteiner, E., Sehling, K. Stefsky, M. & Fasching, K. 1999. Analyse von bestehenden Kriterien-
und Indikatorenkatalogen für nachhaltige Waldbewirtschaftung sowie Analyse von Gesetzen und
ö ffentlichen Datenquellen zu waldrelevanten Aspekten in Österreich: Hintergrundpapier zur
Erarbeitung eines österreichischen Katalogs von Kriterien und Indikatoren zur Messung der
Nachhaltigkeit der Waldbewirtschaftung in Österreich. Erstellt im Auftrag des PEFC-Österreich.
(Analysis of existing Criteria and Indicator Catalogues for sustainable Forest Management, and
Analysis of Laws and public data sources related to Aspects relevant to sustainable Forest
Management in Austria: Background Paper for the Development of an Austrian Catalogue of Criteria
and Indicators for the Measurement of sustainable Forest Management in Austria. On behalf of PEFC
37. UN-CSD (United Nations Commission on Sustainable Development) 1996. Working List of
Indicators for sustainable Development (as of Sept 1996). UN-CSD, New York.
3 8 . UN-CSD (United Nations Commission on Sustainable Development) 1999. Indicators for sustainable
Development: Framework and Methodologies. Background Paper nº. 3. UN-CSD, New Yo r k .
39. Moiseev, A., Dudley, E. & Cantin, D. 2002. The Wellbeing of Forests: an E-tool for assessing
environmental and social Sustainability. IUCN, Gland, Switzerland and Cambridge, UK.
40. Bechmann, A. 1981. Grundlagen der Planungstheorie und Planungsmethodik. (Basics of the Theory
and Methodology of Planning). Haupt, Bern, Stuttgart.
41. H ü b l e r , K.-H., Otto-Zimmermann, K. 1991. Bewertung der Umweltverträglichkeit. Bewertungsmaßstäbe
und Bewertungsverfahren für die Umweltverträglichkeitsprüfung. (Assessment of environmental
Impacts. Reference Frames and Methods for Assessment in Environmental Impact Assessment). 2nd
edition, E. Blottner, Taunussstein.
42. Usher, M.B. & Erz, W. 1994. Erfassen und Bewerten im Naturschutz. (Describing and assessing in
nature conservation). UTB Wissenschaft, Quelle & Meyer, Heidelberg, Wiesbaden.
43. OECD (Organisation for Economic Cooperation and Development) 1994. Environmental Indicators:
OECD Core Set. OECD, Paris.
44. Bossel, H. 1999. Indicators for sustainable Development: Theory, Method, Application. AReport to
the Balaton Group. International Institute for Sustainable Development, Winnipeg.
45. Noss, R.F. 1990. Indicators for monitoring Biodiversity: a hierarchical Approach. Conserv. Biol. 4: 355-364.
DOI: 10.1111/j.1523-1739.1990.tb00309.x
46. Wildburger, C. & Lebenits, R. 1995. Auswirkungen der Jagd auf den Wald in Österreich. Eine Studie
zum Einfluss der Schalenwildbewirtschaftung auf Waldökosysteme. (Impacts of Hunting on Forests
in Austria. AStudy on the Incfluence of Ungulate Management on Forest Ecosystems). Monographs
of the Umweltbundesamt Vol. 70. Umweltbundesamt, Vienna.
47. Umweltbundesamt 1997. Jagd und Nachhaltigkeit. Ergebnisse des Workshops am 11. Juni 1996,
Hermesvilla, Wien. (Hunting and Sust ainability. Results of a Workshop on July 11 1996,
Hermesvilla, Vienna). Conference Reports Vol. 21. Umweltbundesamt, Vienna.
48. Website “Kriterien und Indikatoren einer nachhaltigen Jagd”. (“Criteria and Indicators of Sustainable
Hunting”). Cited 26 Jul 2004.
49. Harborth, H.J. 1993. Dauerhafte Entwicklung statt globaler Selbstzerstörung. Eine Einführung in das
Konzept der nachhaltigen Entwicklung. (Sustainable Development instead of global self-destruction.
An Introduction to the Concept of sustainable Development). Edition sigma, Berlin.
50. Rennings, K. 1994. Indikatoren für eine dauerhaft-umweltgerechte Entwicklung. (Indicators for
sustainable Development). Metzler-Poeschel, Stuttgart.
51. L e x e r , M.J., Lexer, W. & Hasenauer, H. 2000. The Use of Forest Models for Biodiversity A s s e s s m e n t s
at the Stand Level. Investigacion Agraria Sistemas y Recursos Forestales Vol. 1/2000: 297-316.
52. Röhrich, T. & Hackl, J. 2003. Evaluierung der Österreichischen Strategie zur Umsetzung des
Übereinkommens über die biologische Vielfalt. (Evaluation of the Austrian Strategy for the
Implementation of the Convention on biological Diversity). Reports of the Umweltbundesamt Vol.
186. Umweltbundesamt, Vienna.
53. Umweltbundesamt 2004. Umweltsituation in Österreich. Siebenter Umweltkontrollbericht des
Umweltministers an den Nationalrat. (State of the Environment in Austria. 7th Report of the Minister
of the Environment on the State of the Environment in Austria to the National Parliament.
Umweltbundesamt, Vienna).
54. Reimoser, F., Armstrong, H. & Suchant, R. 1999. Measuring Forest Damage of Ungulates: what
should be considered? Forest Ecol. Manag. 120: 47-58.
DOI: 10.1016/S0378-1127(98)00542-8
55. Reimoser, F. 2000. Income from Hunting in Mountain Forests of the Alps. In: Price, M.F. & Butt, N.
(eds.). Forests in sustainable Mountain Development: a state-of-knowledge Report for 2000. IUFRO
Research Series, no 5, CABI Publishing, New York. pp. 346-353.
56. Raesfeld, F.V., Neuhaus, A.H. & Schaich, K., 1985. Das Rehwild - Naturgeschichte, Hege und Jagd.
(Roe deer – natural history, preservation and hunting). Paul Parey, Hamburg und Berlin.
57. Reimoser, F. 1999. Wildlife Ecological Spatial Planning (WESP): an Instrument for integrating
Wildlife into comprehensive Land Management. In: Proceedings of the International Union of Game
Biologists, XXIVth congress, Thessaloniki, Greece. pp. 176-185.
58. Kollmann, G., Leuthold, M., Pfefferkorn, W. & Schrefel, C. 2003. Partizipation: ein Reiseführer für
Grenzüberschreitungen in Wissenschaft und Planung. Schriftenreihe Integrativer Tourismus und
Entwicklung Bd. 6. Respect – Institut für Integrativen Tourismus und Entwicklung, Wi e n .
(Participation: a Travel Guide for Frontier Crossings in Science and Planning. Series Integrated To u r i s m
and Development Vol. 6. Respect – Institute of Integrated Tourism and Development, Vi e n n a ) .
59. Kellert, S. & Brown, P. 1985. Human Dimensions Information in Wildlife Management, Policy and
Planning. Leisure Sci. 7 (3): 269-280.
60. Schulz, W. 1988. Sozio-ökonomische Untersuchungen für Wildtiermanagement und Naturschutz. (Socio-
economic Investigations for Wildlife Management and Nature Conservation). Z. Jagdwiss. 34: 1-11
DOI: 10.1007/BF02241275
61. Manfredo, M.J., Vaske, J.J. & Sikorovski, L. 1996. Human Dimensions of Wildlife Management. In:
Ewert, A . W. (ed.). Natural Resource Management: the Human Dimension. Westview Press. pp. 53-72.
62. Linser, S. 2001. Critical Analysis of the Basics for the Assessment of sustainable Development by
Indicators. PhD Thesis, University of Freiburg.
63. Cairns, J., McCormick, P.V. & Niederlehner, B.R. 1993. Aproposed Framework for developing
Indicators of Ecosystem Health. Hydrobiologia 263: 1-44.
DOI: 10.1007/BF00006084
64. Lexer, W. 1998. Ökologische Anforderungen an eine nachhaltige Raumentwicklung. Diplomarbeit,
Universität für Bodenkultur (BOKU), Wien. (Ecological Requirements for sustainable spatial
Development. MSc Thesis, University of Natural Resources and Applied Life Sciences (BOKU),
65. Bastian, O. & Schreiber, K.-F. 1999. Analyse und ökologische Bewertung der Landschaft. (Analysis
and ecological Assessment of Landscapes). Spektrum Akadem.Verl., Heidelberg, Berlin.
66. Bechmann, A. 1995. Anforderungen an Bewertungsverfahren im Umweltmanagement – Dargestellt
am Beispiel der Bewertung für die UVP-Dokumentation zu den 11. Pillnitzer Planergesprächen am
29.-30. Sept. 1995: 6-39. (Requirements for Assessment Methods in environmental Management –
demonstrated by the Example of the Documentation of Environmental Impact Assessment at the 11th
Planner´s Debate, Sept. 29-30 1995: 6-39).
67. Nipkow, M. 1997. Synoptisches Bewerten im Naturschutz: Ein multivariater Verfahrensansatz.
(Synoptical Assessment in Nature Conservation: a multivariate methodical Approach). NNA-
Berichte 10: 101-105
68. Leitner, H. & Reimoser, F. 2000. Grundsätze der Winterfütterung. (Principles of Winter Feeding).
Österreichs Weidwerk 2000 (9): 8-12.
69. IUCN (The World Conservation Union) 1996. Assessing Progress toward Sustainability. Methods
and Field Experiences. An IUCN/IDRC project. IUCN, Gland.
... Within each sector, principles are made operative with a certain number of criteria, and these in turn through a certain number of indicators (see Fig. 9). Thus, the degree of specificity and targeting of actions increases from the top of the assessment pyramid towards the base ( Lexer et al., 2006). The actual assessment is made at the lowest level, that of the indicators, through a system of point scores (see Section 4.2.3). ...
... There is no weighting of indicators beyond this level. These weightings were deter- mined as part of the participatory process accompanying the project, in co-operation with the stakeholders ( Lexer et al., 2006;Reimoser et al, 2003). The evaluation is completed by simp- ly adding the point scores for all indicators. ...
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Wild animals and their habitats are exposed to multiple impacts caused by hunting and many other often overlapping and competing land-use activities within the wildlife habitat. In particular in multiple-use cultural landscapes the interaction between the habitat requirements of wild animals, hunting interests and other land-uses often leads to conflicts that can negatively affect the sustainable conservation of native wild animal species and their habitats, the sustainability of some types of land use and of wider regional development. Stand-alone sectoral approaches to sustainable use are insufficient and often result in unintended adverse effects on other land use sectors and the relevant ecosystems. In contrast, sustainable wildlife management requires that all land-user groups in the wildlife habitat are aware of and consider the effects of their activities on both wildlife resources and other user groups. With this in mind, concepts and tools for the integrated sustainability assessment of several land-user groups have been developed in the model region “Wienerwald Biosphere Reserve”, using the relationship between wild animals and hunting as an example. The Wienerwald Biosphere Reserve is an intensively used area for a variety of activities (particularly forestry, agriculture, hunting, and a number of leisure activities) sited near to Austria`s capital Vienna, and (as specifically envisaged for biosphere reserves) the main aim is the development and implementation of sustainable land use concepts. Applied and participatory research methods have been used to identify, analyse and evaluate key interfaces and linkages (both antagonistic and synergistic) between wildlife populations, wildlife habitats and different forms of regional land use. The main project outputs are four operational sets of principles, criteria and indicators for integrated sustainable wildlife management, focused on the major regional land-user groups forestry, agriculture, hunting, and recreational management. Hunting can have also a strong recreational aspect, but is seen here as a separate land use activity including professional and recreational hunting as well as consumptive and nonconsumptive use of natural resources. These four assessment sets are harmonised across the land-use sectors and designed as self-evaluation tools; they are to be applied by each of the four land-user groups in order to evaluate their respective influence on the sustainable conservation of wild animal species, their habitats and sustainable hunting. The assessment framework of each group also considers relevant sustainability requirements of other user groups. By focussing on the crosscutting issue of wildlife management, the step from sector-specific towards cross-sectorally integrated assessment of sustainable use has been taken for the first time. Moreover, recommendations for integrated sustainable wildlife management and for respective monitoring have been elaborated. Project results should contribute to the avoidance, mitigation and resolution of wildlife land-use conflicts and to the integration of wild animals and their management into a sustainable regional land-use system. The land user groups of the model region comprise private, community, and public organizations.
... Standalone sectoral approaches to sustainable use are insufficient and often result in unintended adverse effects on other land-use sectors and the relevant ecosystems. In contrast, sustainable wildlife management requires that all land-user groups in the wildlife habitat are aware of and consider the effects of their activities on both wildlife resources and other user groups [1][2][3]. ...
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Tools for an integral sustainability assessment of four different land user groups have been developed in the Austrian model region “Vienna-Woods Biosphere Reserve”. Focusing on the cross-cutting issue of wildlife management, the step from sector-specific towards cross-sectoral integrated assessment of sustainable use has been taken for the first time. The assessment tools are also suitable for wider application if indicators are adapted to the specific region. / Keywords: Land use, wildlife, sustainability, indicators, assessment, method. / Published in: Agricultural Research & Technology - Open Access Journal (ISSN: 2471-6774), Volume 25, Issue 4
... Defensores da caça argumentam que muitos animais caçados morreriam de qualquer maneira, talvez com maior sofrimento (predados, doentes ou por inanição); que o máximo é feito para reduzir o sofrimento, que a prática é um direito que não pode ser sujeito a uma licença social; que caçadores são pessoas civilizadas exercitando habilidades humanas distintivas, inteligência e virtudes como a paciência e disciplina emocional (Causey 1989). Além de evitar o colapso do recurso explorado, exige-se da prática da caça a preocupação ainda com uma série de outras questões, como a introdução ou dispersão de espécies exóticas; a contaminação; a indução de pressões seletivas; o sofrimento animal; o respeito a comunidades e tradições locais; os efeitos em cascata nas comunidades biológicas e ecossistemas; a saúde humana; os conflitos com outros usos da terra, respeito e direitos de comunidades tradicionais; o combate à pobreza e exclusão social e outros (IUCN/PACO 2009, Lexer et al. 2005. Tais exigências não são peculiares da caça, mas válidas e também eventualmente contestadas para outros tipos de exploração de recursos naturais ou reivindicações ambientais, dependendo da "localização social" de cada grupo ambientalista (Taylor 2000). ...
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To hunt or not to hunt, here is the question. Few issues raise as much conflict of opinion in the environmental arena as hunting. There are numerous forms of hunting in a diffuse gradient of interests, methods, social and environmental effects, degrees of formalization and degrees of social acceptance. The modern debate on hunting, including in Brazil, focuses on moral issues, but environmental and social issues are gaining relevance. A reflection on hunting goes through the overcoming of ambiguous forms such as biodiversity and animals are represented in modern societies. Being a newly incorporated theme in the ethical domain, this is a field still under construction on which there is no unified morality. In this article I argue that (1) there is a great deal of diversity of relationships between humans and animals and of motivations for these relationships in modern societies, in such a way that the concept of hunting must always be referred to an explicit context; (2) arguments and judgments in favor or against particular types of hunting include contradictions and conflicts with those used in other environmental issues; (3) superficial treatment of the topic and lack of consensus often result in improperly grounded positions and decisions; (4) the dominant modern social construction is conditioned by the urban way of life, which is characterized by a departure or even alienation of first-hand contacts with wild environments and species, emphasizing the notion of cruelty; (5) that all forms of hunting present challenges and opportunities for the satisfaction of social interests and contribution or threat to the conservation of biodiversity, so it is not possible to judge a priori any type of hunting as in itself conservationist or degrading.
... The results of this case study highlight that a successful reduction of cervid populations can be achieved by: (1) the longterm monitoring of species abundance by wildlife management authorities as the basis for implementing changes in hunting practices and setting annual hunting quotas (Fig. S3 Online Resource 1) and (2) the coordination of management actions over areas of appropriate size (Meisingset et al. 2017) (in this study, a red deer management area of 17.500 ha). Given the increasing bag records of ungulates, including roe deer and wild boar [Sus scrofa] in Europe (Apollonio et al. 2010b;Vetter et al. 2015), white-tailed deer [Odocoileus virginianus] in North America (Simard et al. 2013), and sika deer [Cervus nippon] in Asia (Ueno et al. 2010), and a decline in public acceptance of hunting activities (Lexer et al. 2005), (2006)(2007)(2008)(2009)(2010)(2011)(2012)(2013)(2014)(2015) and without (1999)(2000)(2001)(2002)(2003)(2004)(2005) an adaptive management approach in the Southern Black Forest our results will contribute to an understanding of the role of hunting in adaptive management. ...
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Numerous studies have addressed the question of whether hunting is capable of limiting the abundance of ungulates in the northern hemisphere. We investigated whether the hunting of red deer (Cervus elaphus) has reduced their abundance in the Southern Black Forest (area 17,500 ha), Southern Germany, since 2006. Red deer abundance was estimated using data obtained from visual counts at winter feeding sites, track counts, and bag records. An age- and sex-structured population model to estimate the winter population size was also constructed using bag records. The estimated red deer population size was evaluated according to a non-invasive genetic mark-recapture approach. The results showed that the hunting of red deer can reduce their population size if the hunting regime is part of a holistic management concept that takes into account the uncertainty of population size estimates and is implemented at scales appropriate to the management of this species.
... Tools also need to be developed that are capable of analyzing the environmental factors interacting with the damage that occurs (Bugmann and Weisberg 2003). Indeed, although the increasing deer population may explain the rise in the level of bark stripping damage, the evolving characteristics of the ungulate habitat cannot be overlooked as a contributory factor (Reimoser et al. 2003). ...
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• Context Over the past few decades, the impact of large herbivorous ungulates on forest vegetation has been clearly highlighted. Among those impacts, bark stripping of coniferous trees is one of the most damaging. Bark stripping leads to rot development, inducing serious loss of timber value. • Aims The present study aimed firstly at evidencing the factors explaining the variations observed in fresh bark peeling rate for spruce and Douglas-fir in southern Belgium and secondly at identifying the key factors to consider when setting up a deer management plan. • Method Fresh bark peeling rate was recorded with a systematic sampling survey from 2004 to 2007. The covered territory was then divided into 63 distinct hunting zones of area ranging from 1,000 to 25,000 ha. About 5,000 plots were monitored annually. Each zone was characterized with a large number of explanatory variables. The explanatory variables were integrated firstly into fixed linear models using a stepwise procedure, and then into a mixed model. • Results The significant variables included in the model (R 2 = 44 %) are (by decreasing order of importance) red deer densities, proportion of coniferous stands and agricultural areas, snow cover, distance to urban habitats, and species diversity in the understory. • Conclusion The models revealed the impacts of several factors on bark peeling: deer density, deer-carrying capacity of the territory, landscape structure, and severity of winter conditions. The adjusted model allowed subtracting the impact of winter conditions in order to produce a relevant indicator for hunting management. In addition, the model was used to assess the sensitivity of a forested area to bark peeling based on its environmental characteristics.
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Ziel des Kriterien- und Indikatorensets ist es, auf transparente, praxisgerechte und zeiteffiziente Weise die selbstständige Überprüfung der Nachhaltigkeit der eigenen Jagdausübung zu unterstützen. Dies soll die Feststellung individueller Stärken und Schwächen und die Ableitung von Maßnahmen zur Optimierung der Nachhaltigkeit erleichtern. Um eine möglichst breite Anwendung durch die Betroffenen zu ermöglichen, wurde eine benutzerfreundliche Möglichkeit zur Selbstbewertung im Internet verfügbar gemacht ( Aufbauend auf Vorarbeiten (UMWELTBUNDESAMT, 1997), internationalen methodischen Standards für umweltrelevante Prinzipien, Kriterien und Indikatoren, internationalen Übereinkommen und Initiativen, wie der CBD sowie nationalen Umsetzungsstrategien – wurden 13 konkrete Prinzipien, 24 Kriterien und 51 Subkriterien (P, K, I) mit Indikation und Wertung definiert. Ein in mehreren Schritten ausgeweiteter Prozess der Partizipation erlaubte es einem großen Kreis von Personen aus allen betroffenen Interessengruppen, zu diesem Set Stellung zu nehmen und Ideen und eigenes Wissen einzubringen. Die Nachhaltigkeitsbewertung bezieht sich auf die jagdliche Tätigkeit und auf die dem Jagdrecht unterliegenden wild lebenden Tierarten. Andere Tierarten, die mit jagdrechtlich relevanten Wildarten in enger ökologischer Wechselbeziehung stehen, können indirekt mit angesprochen sein. Schnittstellen zu nicht jagdlichen Nutzungssektoren werden zwar bewusst angesprochen, aber nur im Hinblick auf den jagdlichen Einflussbereich bewertet. Die vorrangige Beurteilungseinheit für die Bewertung einer nachhaltigen Jagd mit Hilfe der P, K, I ist das Jagdgebiet oder die Hegegemeinschaft. Die Auswertung ist aber grundsätzlich auch für größere – z. B. regionale – Gebietseinheiten möglich. Das Set der Prinzipien und die Bewertungsmethodik sind generell anwendbar. Durch Modifikation einzelner Kriterien und Indikatoren kann das gesamte Bewertungsset auch an nicht-europäische Verhältnisse und andere jagdrechtliche Ausgangssituationen angepasst werden. Im ökologischen Bereich orientieren sich die P, K, I an der Erhaltung und Verbesserung der Wildlebensräume, der Artenvielfalt des Wildes und der genetischen Vielfalt der Wildarten. Im ökonomischen Bereich der Jagd ist die Sicherung der jagdwirtschaftlichen Ertragsfähigkeit und Rentabilität ein Hauptziel. Für Jagdeigentümer und Verpächter ist das Verhältnis zwischen monetären Aufwendungen und Erlösen des Jagdbetriebes ausschlaggebend für die wirtschaftliche Bilanz, während für Pächter und Jagdkunden neben den Kosten insbesondere der subjektive immaterielle Nutzen (Naturerleben, Erholungswert etc.) in die Bilanz eingeht. Die Orientierung der Jagdausübung an der Wildschadenanfälligkeit land-, forst- und fischereiwirtschaftlicher Kulturen ist ein wichtiges Merkmal einer ökonomisch nachhaltigen Jagd. Dies erfordert die regelmäßige, wechselseitige Abstimmung mit anderen Landnutzern. Im sozio-kulturellen Bereich wird auf den Interessenausgleich innerhalb der Jagdausübungsberechtigten, auf die aktive Einbeziehung von Grundeigentümern und anderen örtlichen Nutzer- und Interessengruppen, auf die Beziehung zwischen Jägern und Nicht-Jägern innerhalb der Gesellschaft, auf das Wohlergehen der Wildtiere sowie auf jagdethische und jagdkulturelle Aspekte eingegangen. Das Bewertungsset ist als lernendes, dynamisches System konzipiert, das eine laufende Verfeinerung ermöglicht und dessen Indikatoren an regionale Verhältnisse angepasst werden können. Die Ergebnisse können mit den statistischen Ergebnissen von Monitoringsystemen kombiniert werden. Der vorliegende jagdspezifische Nachhaltigkeitsansatz sollte zukünftig mit Nachhaltigkeitskriterien anderer Landnutzungssektoren verknüpft und so sukzessive in eine sektorübergreifende Gesamtnachhaltigkeitsstrategie eingebunden werden.
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The objective of the set of principles, criteria and indicators is to function as a supporting instrument for transparent, practice-oriented and time-efficient assessment of one´s own practice of hunting. Thereby, it should facilitate the analysis and ascertainment of individual strengths and weaknesses, as well as actions to optimise sustainability. Based on previous work, such as “Basics for Principles, Criteria and Indicators of Sustainable Hunting” (UMWELTBUNDESAMT, 1997), on international standards for environmental principles, criteria and indicators as well as on international conventions and initiatives, such as the CBD, 13 clear principles, 24 criteria, and 51 sub-criteria and indicators with scores have been defined. A process of participation that was gradually extended allowed a large circle of persons from all relevant stakeholder groups to express their views and contribute their own ideas and experience. This sustainability assessment is concerned with hunting activities and all those wildlife species that are subject to hunting laws (game animals). Other wildlife species in close interaction with wildlife species subject to hunting laws may also, indirectly, be included. Interfaces with land use sectors other than hunting are, although deliberately addressed, assessed only in terms of the influence hunting itself can have on them. The primary unit to be used for assessing sustainable hunting with principles, criteria and indicators is the hunting management unit (hunting ground, “hunting ring”). However, assessment is basically also possible for larger areas, e. g. on a regional scale. The set of principles as well as the assessment methodology can be made standard practice. By modifying certain criteria and sub-criteria, the entire assessment framework can be adjusted to non-European circumstances and different hunting systems. As far as ecological aspects are concerned, the guiding principles of the principles, criteria and indicators are the conservation and improvement of game habitats, game species diversity, and of the genetic diversity of game species. Securing a capability for producing returns and the profitability of hunting is one of the major objectives of economically sustainable hunting. For owners of hunts and for those granting hunting leases, the monetary expense/yield ratio of a hunting operation is important for the final balance, whereas for tenants and hunting customers the subjective immaterial benefit derived from hunting (nature experience, recreational value, etc.) is important, apart from the expense. Taking into account the susceptibility of agricultural crops, forest stands and fisheries to damage by game is an important characteristic of economically sustainable hunting. This requires harmonising hunting activities with other land use sectors and their representatives (e. g. agriculture and forestry, tourism, transportation) on a regular and mutual basis. With regard to socio-cultural aspects, the balancing of interests among the hunters themselves and the active involvement of landowners and other local user and interest groups are considered. Several indicators also refer to the relationship between hunters and non-hunters within society as a whole, to the well-being of wild animals as well as ethical and cultural aspects related to hunting. In future, the hunting-specific approach to sustainability as described here should be linked up with the sustainability requirements of other sectors of land use, and thereby gradually integrated into an overall cross-sectoral sustainability strategy.
Game birds such as pheasants Phasianus colchicus (Horsfield) are bred and released to supplement wild living populations prior to the hunting season. The total bag records of these birds are, therefore, not suitable for monitoring the development of wild populations because they are heavily influenced by game management. Wild and released pheasants can be expected to be genetically similar or identical to wild birds because wild birds are captured and used for breeding. It is, therefore, not possible to use genetic methods for identifying released individuals. Heavy stable isotopes are incorporated in animal tissues in a predictable manner and depend on the concentration of heavy isotopes in the diet. The heavy isotopes 13C and 15N accumulate in the food chain because the more common lighter isotopes are excreted at a higher rate than the heavy isotopes. Bred and released pheasant feed on a uniform plant-based diet, and it can, therefore, be expected that these animals have lower and less variable levels of heavy isotopes than individuals from a wild populations which feed on a diverse diet of plants and invertebrates. We investigated the isotope signatures in feathers from wild and released pheasant populations and compared the levels and variation in isotope signature amongst the populations. Bred and released pheasants are clearly identified in comparison to released pheasants as wild types have higher δ 15N.
Conference Paper
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WESP, a conception of spatial planning and integral management was developed at the Institute of Wildlife Ecology, Vienna, and was initially applied to management of red deer (Cervus elaphus), roe deer (Capreolus capreolus), chamois (Rupicapra rupicapra), and ibex (Capra ibex) in Austria's provinces Vorarlberg and Salzburg, and contiguous parts of adjoining countries (Duchy of Liechtenstein, Switzerland). Planning is systematically subdivided into: (a) country-wide basic planning; (b) detailed regional planning; and (c) international coordination of measures. The main aims of WESP are protection of game habitats and the avoidance of game damage to forests by achieving a better distribution of ungulate game and lessening negative landuse impacts. The most important planning criteria and management principles are demonstrated. The objectives include: • Safeguarding the survival of indigenous wildlife populations under conditions appropriate to the biotope and species; • Improving wildlife habitats; • Maintaining regionally typical vegetation by preventing damage caused by wildlife; • Optimizing and co-ordinating diverse forms of land use and sustainable use of natural resources in an ecologically and socio-economically acceptable fashion; • Enabling sustainable utilization of wildlife resources; • Solving conflicts at a local level interactively with all interest groups concerned.
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Biodiversity is presently a minor consideration in environmental policy. It has been regarded as too broad and vague a concept to be applied to real-world regulatory and management problems. This problem can be corrected if biodiversity is recognized as an end in itself, and if measurable indicators can be selected to assess the status of biodiversity over time. Biodiversity, as presently understood, encompasses multiple levels of biological organization. In this paper, I expand the three primary attributes of biodiversity recognized by Jerry Franklin — composition, structure, and function—into a nested hierarchy that incorporates elements of each attribute at four levels of organization: regional landscape, community-ecosystem, population-species, and genetic. Indicators of each attribute in terrestrial ecosystems, at the four levels of organization, are identified for environmental monitoring purposes. Projects to monitor biodiversity will benefit from a direct linkage to long-term ecological research and a commitment to test hypotheses relevant to biodiversity conservation. A general guideline is to proceed from the top down, beginning with a coarse-scale inventory of landscape pattern, vegetation, habitat structure, and species distributions, then overlaying data on stress levels to identify biologically significant areas at high risk of impoverishment. Intensive research and monitoring can be directed to high-risk ecosystems and elements of biodiversity, while less intensive monitoring is directed to the total landscape (or samples thereof). In any monitoring program, particular attention should be paid to specifying the questions that monitoring is intended to answer and validating the relationships between indicators and the components of biodiversity they represent.
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Considerations involved in developing a suite of indicators to monitor regional environmental health, similar in conception to management use of leading economic indicators, are described. Linkages between human activities and well being and the state of the environment are considered essential to the evaluation of general environmental health. Biogeochemical and socioeconomic indicators are mutually affected by environmental degradation and examples of both categories of indicators are described. Desirable properties in indicators of environmental health vary with their specific management use. Different indicators are called for when collecting data to assess the adequacy of the environment, monitor trends over time, provide early warning of environmental degradation, or diagnose the cause of an existing problem. Tradeoffs between desirable characteristics, costs, and quality of information are inevitable when choosing indicators for management use. Decisions about what information to collect for which purpose can be made more rationally when available indicators are characterized and matched to management goals.
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Sustainability in the 21st century is seen as basis for the use of natural resources. In European countries evaluation criteria for sustainable use are developed in various sectors (e.g. agriculture, forestry, fishing, tourism). For wildlife management and hunting an unsatisfied need in defining sustainability existed. Therefore in the course of an interactive, particapatory stakeholder-process the authors developed an assessment framework that allows hunters to evaluate the degree of sustainability of their own individual hunting practices. Based on international and national obligations and provisions (e.g. CBD, MCPFE, IUCN), a transparent set of ecological, economic and socio-cultural principles (11), criteria (20), and subcriteria (39), with indicators and assigned values, has been defined. Main task of the assessment set is to function as a decision-supporting and awareness-raising instrument for managers of hunting grounds or hunting communities in order to identify sustainability gaps, to provide guidance in deducing measures for more sustainable future hunting practices and to measure progress in the implementation of sustainability requirements. The results are available for a broader range of users and for further sophistication via WorldWideWeb ( In this paper the new method (procedural and organizational framework, architectural structure of assessment model) is presented. The participatory, interdisciplinary social bottom-up working process that involved a large number of interest groups and experts is seen as a crucial factor promoting acceptance. Strategic backgrounds of the study results, evaluation method, and interpretation basics are described. Major attributes in contents as well as possibilities for further development of the test system are outlined.
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Principles and criteria for the objective assessment of `damage' are presented as a basis for objective discussion and to promote targeted research. The topic will be considered from three different viewpoints – theoretical background, silviculture, and nature conservation. Examples of methods to assess `damage' are given, as are the criteria and indicators for target values for growing stock.The objective existence of damage must be established by comparing the current status against a target. Only if the present status no longer permits achievement of the desired target can damage be claimed. The same is true for verification of `benefit' resulting from an impact leading to a favorable status. Establishing the degree of browsing damage on forest regeneration allows forecasts of damage to be made, but the actual damage can only be determined at a future time, for example when the timber is harvested or when the function of the forest is seen to have been compromised. The earlier the forecast is made the more uncertain it is, because the compensatory responses of the forest can only be forecast to a limited extent. Silvicultural targets depend on the requirements of both, the forest owner and the public. Main indicators for assessing ungulate damage on forest regeneration are total tree density, species composition, and height structure. From the viewpoint of nature conservation the determination of target values is particularly difficult. The measurement of damage involves choosing the most relevant indicators of favorable condition of woodland habitats and assessing these in the field. With adequate resources this can be done quantitatively using a wide range of standard field measurement techniques. Alternatively, where resources are limited, it can be done qualitatively by scoring different areas for a range of indicators. As yet, such qualitative methods are in their infancy. Specific research is now being undertaken in some European countries.
“The process of finding, implementing, and improving sustainable development indicators will not be done right at first. Nevertheless, it is urgent to begin.” (MEADOWS 1998: 78) SUMMARY: The Agenda 21, which was agreed upon by 179 nations at the United Nations Conference on Environment and Development (UNCED) in 1992 in Rio de Janeiro stands for a comprehensive program for action. It lines out the guiding principles for a sustainable development in the twenty-first century. Sustainability indicators have a special importance for the definition and assessment of the targets as well as for the monitoring of the implementation of the requirements stated in the agreements of the Agenda 21. Based on the experiences of the follow-up process of the UNCED the theoretical and methodological bases for an elaboration of indicators is analyzed in this study. Conclusions are drawn about the practicability of the underlying models. The theoretical part is completed by an empirical consolidation. The exposition is structured in seven main chapters: The problem of assessing development respectively the assessment of sustainable land use is described in chapter one, concluding in the following targets of this study: • a detailed description of the so far international and national applied theoretical framework for the elaboration of indicators and corresponding models, • a specification of the concepts and constraints of sustainable development, • a detailed representation and critical reflection of the basics and requirements for sustainability indicators, and • an empirical verification of the theoretical results by expert interviews. Chapter 2 outlines the theoretical framework for indicators. The definition of indicators is exemplified by deductive and inductive approaches. A retrospective view on the different stages of the development of indicators facilitates the classification of various types of indicators. Main functions of indicators are derived and explained based on literature research. Threshold degrees and limiting values are introduced as normative aspects of indicators. The clarification of the differentiation characteristics of indicators, the description of the process of indicator selection, as well as the criteria of choice are a main part of the theoretical foundation. The chapter is completed by a critical discussion of the demand, intention and methods of aggregation. Following the theoretical explanations for the elaboration of indicators in general, chapter 3 concentrates on the basics and requirements for sustainability indicators. Sustainable development is interpreted by various definitions. The concepts of sustainable development are enlightened in a system theoretical context. Various constraints which restrict possible paths of development to an accessibility space are explained. Two models of sustainable development are represented to illustrate these insights. Requirements of sustainability indicators are described to meet the methodological and textual demands of the guiding principle of sustainable development independent of a distinctive definition. Further on, the functions of sustainability indicator systems are specified and user groups are distinguished. In chapter 4 various models for the derivation of indicators are introduced and their suitability for the derivation of sustainability indicators is discussed. Different approaches can be distinguished according to ecological or systemic orientation. Ecologically based models result in indicators clarifying external effects on the quality of the natural respectively human environment. Such models are, for instance, the STRESS model of Friend and Rapport, the Pressure-State-Response model of the Organization for Economic Co-operation and Development, the Actor-Acceptor model of Zieschank et al. or the Man-Environment-Man model of the German Federal Statistical Office. Models based on systems theory and therefore able to clarify complex cause-effect interactions are, for example, the model of Ecological Critical Levels and Critical Loads of the United Nations Economic Commission for Europe or the model of Syndromes of Global Change of the German Advisory Council of Global Change and the Potsdam Institute for Climate Impact Research. Chapter 5 concentrates on the design of the empirical analysis. The theoretical requirements for the qualitative data acquisition are described in detail. This chapter comprises justifications concerning the method of structured expert interviews according to the Delphi-method as well as the choice of the German and Finnish interview partners. The main unit of chosen experts, their answering behavior, as well as the circle of respondents are described in detail. The guiding research questions and the development of the questionnaire as the methodological base of the empirical analysis is lined out. The procedure of the data analysis is explained. In chapter 6 the results of the empirical analysis are represented and interpreted. According to the experts the Brundtland-definition of sustainable development is not seen as an appropriate starting point for the elaboration of sustainability indicators. The functions of indicators were revised and completed on the basis of the expert opinions. As an other result of the expert interviews illusions of indicators were compiled for the first time. The limitations of indicator systems are also represented. According to the interviewees indicator systems are suitable to control the success of the implementation of the requirements stated in the agreements of the Agenda 21 only with restrictions. In spite of these problems no alternatives are seen to indicator systems for controlling the success of the implementation of the requirements stated in the agreements of the Agenda 21 on an international level. On a lower level it was emphasized that there are several other means, which could be used parallel to indicator systems. In this context problems which have to be faced to implement a sustainable development are characterized. Concerning relevant decisions on the path towards a sustainable development the wide majority of the experts see the necessity of fair compromises within the participative decision-making process. The ability of indicator systems illustrating the present situation was stressed by the experts, though depending on the quality of the underlying data. Indicators are seen to have a certain force of expression even without relating to threshold degrees that have to be met or which could be used as a basis for comparison. Indicators are seen as appropriate bases for decision-making, however not as a single data but within an operational, easily comprehensible indicator system considering all relevant factors but dependent on the quality of the data. Finally, the criteria of choice for the selection of indicators, listed in chapter 2.7.2, could be verified by the expert opinions, however, with a different ranking. The theoretical framework, the results of this study as well as the methods applied are discussed in chapter 7. Based on the theoretical considerations and the insights gained from the empirical analysis conclusions are drawn for the further elaboration of indicator systems. The qualitative, structured expert interviews according to the Delphi-method have been proven satisfactory to verify the results of the literature research and for the inquiry of actual expert opinions in comparison to similar surveys. This exposition demonstrates and faces the complexity of the process towards a sustainable development. Important guidelines and impulses are provided for the field of applied indicator research beyond a theoretical analysis of the current situation. The results may be particularly important for all those who are actively involved in participatory processes concerning the elaboration of indicator systems which are appropriate for the assessment of a sustainable development.