Journal of Threatened Taxa |
www.threatenedtaxa.org | 26 May 2021 | 13(6): 18441–18452
ISSN 0974-7907 (Online) | ISSN 0974-7893
(Print)
https://doi.org/10.11609/jott.6107.13.6.18441-18452
#6107 | Received 06 May 2020 | Final received
14 March 2021 | Finally accepted 30 March 2021
Patterns, perceptions, and
spatial distribution of human-elephant (Elephas maximus) incidents in
Nepal
Raj Kumar Koirala 1, Weihong Ji 2, Yajna Prasad Timilsina
3 & David Raubenheimer 4
1,3 Institute of Forestry, Tribhuvan
University, Pokhara, Nepal.
1,2 School of Natural and
Computational Sciences, Massey University, Auckland, New Zealand.
4 The Charles Perkins Centre,
University of Sydney, Sydney, NSW, 2006, Australia.
1 rkkoirala@iofpc.edu.np (corresponding autor), 2 J.J.Weihong@massey.ac.nz,
3 yajna.timilsina@pc.tu.edu.np, 4 david.raubenheimer@sydney.edu.au
Editor: Priya Davidar,
Sigur Nature Trust, Nilgiris,
India. Date of publication: 26 May 2021 (online
& print)
Citation: Koirala, R.K., W. Ji, Y.P. Timilsina & D. Raubenheimer (2021). Patterns, perceptions, and
spatial distribution of human-elephant (Elephas maximus) incidents in
Nepal. Journal of Threatened Taxa 13(6): 18441–18452. https://doi.org/10.11609/jott.6107.13.6.18441-18452
Copyright: © Koirala et al. 2021. Creative Commons Attribution
4.0 International License. JoTT allows unrestricted use, reproduction, and
distribution of this article in any medium by providing adequate credit to the
author(s) and the source of publication.
Funding: Rufford Small Grant Foundation, UK; Chester
Zoo, UK.
Competing interests: The authors
declare no competing interests.
Author details: Raj Kumar Koirala is a conservation ecologist
teaching conservation biology and forest zoology and research in the field of animal diet and
nutritional ecology. He is an associate professor at the institute of Forestry, Tribhuvan
University, Pokhara campus , Pokhara, Nepal and a post
doctoral associate at the School of Natural and Computational Sciences,
Massey University, Albany Campus , Auckland, New Zealand. Weihong Ji is a behavioural ecologist
teaching conservation ecology and
research in the field of animal behavioural ecology
and human-wildlife interactions. She is an associate professor at the School of Natural and Computational Sciences,
Massey University, Albany Campus , Auckland, New Zealand. Yajna
Prasad Timilsina is a statistician teaching
experimental design, research methodology. He is a professor at the institute of forestry,
Tribhuvan University, Pokhara campus , Pokhara, Nepal. David Raubenheimer is an expert in nutritional ecology. He
is a professor and Leonard P. Ullman
Chair in nutritional ecology in the Charles Perkins Centre and School of Life
and Environmental Sciences at the University of Sydney. Australia.
Author contributions: RKK and WJ designed the study;
RKK collected the data; RKK, DR, YT and WJ
analyzed the data. RKK wrote the manuscript, and all authors contributed
to the editing of final version of the paper. All authors read and approved the
final manuscript.
Acknowledgements: We thank the Institute of
forestry, Tribhuvan University, Department of National Park and Wildlife
Conservation, the government of Nepal, and the School of Natural and
Computational Sciences, Massey University, Albany Campus, Auckland, New
Zealand. for their support. We also
thank Rufford Small Grant Foundation, UK, Chester
Zoo, for their funding support for the elephant work.
Abstract: Nepal has an estimated population
of 109 to 142 wild Asian Elephants Elephas maximus L.. We carried out a survey of human-elephant
incidents (HEI) of conflict in the buffer zones of Chitwan National Park and Parsa National Park Nepal, using a structured
questionnaire, focal interviews, and secondary data collection. Furthermore, data of HEI were also extracted
from published literature in order to analyse spatial-temporal patterns of
competition throughout Nepal. Elephant
related incidents were higher in the pre-winter season and concentrated along
the southern forest boundary; incidents decreased with increasing distance from
the park/reserve. Crop damage by
elephants occurred in pre-monsoon and winter seasons with the most impact on
rice (the major crop). Bulls (single or
in pairs) were involved in crop raids (44%), property damage (48%), and human
casualties (8%); family herds were only recorded to have raided crops (39%) and
damaged properties (36%). The average
herd size recorded was 10 individuals, with a maximum group size of ≤22
elephants. Generally, incidents per
elephant was high in western Nepal, whereas human and elephant casualties were
higher in central and eastern regions.
To reduce human–elephant incidents 53% of local residents suggested
restoring core and boundary areas with native elephant food plants, 40%
suggested planting alternative crops along park boundaries, 6% favoured
elephant translocation, and only 1% percent was in favour of culling
elephants. Mitigation measures already
in place include wooden watch towers used by villagers to detect elephant
incursions. Low impact traditional
averting techniques, such as drumming and the use of flame torches, were used
to deter intruding elephants at the areas surveyed. In conclusion we suggest potential mitigation
measures such as identifying elephant
refugia and mitigate the impact and assessing the year-round availability of
preferred foods; in addition, we advocate for introducing an equitable
compensation to gain support from local communities adjacent to protected
areas.
Keywords: Asian Elephant, human-wildlife
incidents, endangered species, conservation, questionnaire, stakeholder
solutions.
Introduction
The Asian Elephant Elephas
maximus is among the largest living land mammals and is ‘Endangered’
according to IUCN Red List (Williams et al. 2020). Global estimated population of Asian
Elephants is 41,410–52,345 in the wild and 16,000 in captivity,
distributed across 13 Asian countries (Sukumar 2003; Choudhury et al. 2008). Elephant populations in most of their natural
ranges have been declining with the increase in human populations and land
development causing erosion and degradation of forest habitats (Choudhury et
al. 2008). Such habitat degradation in
the form of deforestation, increases the frequency of incidents with Asian
Elephants (Riddle et al. 2010; Puyravaud et al.
2019), which is hindering conservation efforts in some regions (Hoare 1999; Perera 2009). Thus,
averting habitat destruction and fragmentation is probably most important in
reducing problems with elephants (Hoare 2000; Sukumar 1989, 2006; Puyravaud et al. 2019).
Nepal provides habitat for an
estimated 120–215 Asian Elephants (Pradhan et al. 2011; Koirala et al.
2016). The recent loss of over 80% of
elephant habitat to human settlement (Joshi & Singh 2007), however, has
eroded the carrying capacity. In the
past, elephants were distributed throughout the Terai
forests (Pradhan & Wegge 2007). These forests, which spanned Nepal from east
to west, have now been reduced to 24% of their original size of 593,000ha (Satyal 2004). The
country’s elephant population is now limited to only four areas due to vast
anthropogenic pressure and dwindling resources (Pradhan et al. 2011). Human activities, which encroach on elephant
habitat, also force elephants into direct contact with humans, which results in
adverse incidents (Hoare 1999; Sukumar 2006).
The spatial and temporal nature
of incidents varies within Nepal (Koirala et al. 2016). In central Nepal, the elephant population is
mostly resident. Incidents arising from
crop raids were first recorded in the Parsa Chitwan
area in 1994, when a single bull elephant moved into cultivated agricultural
lands (Velde 1997). Incidents have
increased substantially since then, which poses a serious threat to local people
as well as to resident elephant populations (Pant & Hockings 2013). In
Nepal alone, 66 people and 18 elephants have died as a result, over a period of
16 years, from 1986 to 2002 (Yadav 2007).
In central Nepal, nine people were killed over a period of five years,
from 2008–2012 (Chitwan National Park 2012).
Incidents caused by elephants is the main conservation
issue throughout the elephant’s home range (Hoare 1999). The nature and extent of damage caused by
these animals to humans and vice versa is not clear. In the present study, we examine multiple
aspects of human-elephant incidents in Nepal mostly focussing on central
Nepal. To the best of our knowledge, one
study has identified the spatiotemporal distribution of human–elephant
incidents (HEI) at a national level in Nepal through an indirect measure: by
way of newspaper articles (Neupane et al. 2013). The present study, however, has quantified
the spatio-temporal pattern and perception of
elephant problems by residents using a questionnaire surveys and secondary
data. We consider data reliability for
the former study to be greater for the reporting of human casualties, and
elephant deaths, while our study aimed to generate reliable data on all types
of human-elephant incidents including peoples’ perception on human-elephant
coexistence. Thus, the aim of this study
was, therefore, to assess the magnitude and nature of the human-elephant
incidents and to obtain the opinions and perceptions of local people on
mitigating elephant impacts and on enhancing elephant conservation. To explore these topics, research questions
were asked in relation to type, frequency, and trends in elephant visitations
and damages, with an overall goal of finding local solutions to minimise
competition with humans.
In addition, for the purposes of comparison, we
explored spatial and temporal distribution patterns and the driving forces of
human-elephant incidents in other regions in Nepal.
Materials and Methods
Data were collected between July 2012 and December
2014 in villages distributed throughout the northern and southern buffer zones
of the Chitwan and Parsa National Park (Fig. 1).
Information on human-elephant incidents was collected
through a structured questionnaire designed to document the personal details of
the respondent, their occupation, agricultural practices if any, problems
encountered with elephants, major forms of damage sustained from elephant
visitations (Appendix 1). The details of
the spatio-temporal nature and extent of crop and
property damage and human and elephant casualties, alsthe
timing and frequency of damage, major crops and also plant parts eaten, and
locals’ mitigation methods were requested.
In total, we surveyed 302 households, focussing more
on villages near park boundaries. Every
fifth household within each village was selected, and interviews were conducted
with the head of the household. If the
head of the household was not present, the most senior member of the family was
chosen for interview. If no one was at
home, the next house was selected for interview. Verbal consent of the respondent was obtained
before conducting the interview (Pant & Hockings 2013), and none of the
respondents declined to participate in the survey. All information received was treated as
approximate, since it was based on respondents’ estimates and recollections
(Kulkarni et al. 2010). Altogether, 75
villages under the auspices of 17 village development committees (VDC) were
surveyed within four districts (Chitwan, Parsa, Makwanpur, and Bara).
VDCs were local government bodies in rural Nepal, equivalent to
municipalities in urban areas till 2016.
The Gaunpalika system was established in 2017,
replacing the VDC system that was in use since 1990. The geographical coordinates of the
households where interviews were conducted were obtained by marking their
location using a Garmin eTrex Venture global
positioning system (GPS) unit.
Kangwana (1995) has cautioned that conclusions cannot be drawn
based entirely on farmers’ and householders’ replies to a questionnaire. To validate the household survey records,
secondary interviews information was collected from existing record of
incidents in the park and buffer zone office and focal interview were conducted
with key informants from community and park and buffer zone committee
officials. Their experience and
knowledge of existing elephant populations, HEI causes, measures taken and
potential solution to the problem were recorded.
Furthermore, data of HEI were also extracted from
published literature in order to analyse spatio-temporal
patterns of competition throughout Nepal.
Among four elephant distribution areas, the eastern region was covered
by forest remnants and only 175km2 was under protection. Edge habitat covered 12,892ha (Nepal WWF
2007) while in central Nepal intact forest under protection totalled 3,549km2
with 28,500ha edge habitat in the Chitwan National Park buffer zone (Baidya et al. 2009).
While in western region covering Bankey and Bardia National Parks, patchy forest remnants were
distributed in the south and south-western part of the parks. A total area of 1,437km2 was under
protection at the time of our study.
Forest edge habitat totalled 12,979ha.
The far western area in Shuklaphanta Wildlife
Reserve supported a 305km2 area of intact, fully protected
forest. Forest edge habitat covered
33,554ha, the largest forested edge habitat in Nepal (Nepal WWF 2007).
Data analysis
We examined data over a 10-year period
(2003–2012). Relative incident intensity
among villages was calculated by the relative frequency of different categories
of incidents (crop depredation, property damage, human casualty, and elephant
casualty). The intensity of 3 was the
lowest and 1 was the highest intensity with a combination of different types of
incidents.
The per capita elephant damage rate calculated using
the equation below and used as an index of incident intensity (II).
Frequency of incidents/year
Incident intensity (II) = ––––––––––––––––––––––––
Total number of elephants
GPS location data of HEI were used to prepare a
detailed map in ArcGIS version 10.1.
Chi-square test was used to assess trends in elephant damages, the
respondents’ attitudes towards elephant caused damage and the local perceptions
on elephant conservation. Pearson
correlation tests were conducted to determine the relationship between the
number of crop raiding/property damage incidents and human casualties and the spatio-temporal relationships between elephant damage and
the spatial location of villages. The
IBM statistical package for social sciences (SPSS) version 22 was used to analyse data.
Results
Respondents and their major incident experiences
Of 302 respondents, 258 (85%) were males and 44
(14.6%) were females. A total of 170
(56%) interviewees resided in the buffer zone of Chitwan National Park, and 132
(44%) were within the buffer zone of the Parsa
Wildlife Reserve. The mean age of
respondents was 45 years (n= 302 ± SD= 10) and ranged from 21–73 years. Interviewees were distributed unevenly
between the 17 village development zones: representation by zone ranged from a
low of 1.7% in the Bhandara area in Chitwan to a high
of 12.6% in the Nirmal Basti village development
committee in the Parsa buffer zone.
Respondents reported crop raids to be the most common
form of elephant damage, comprising 77% of total HEI, followed by property
damage (22%) and human casualties (1%) (Fig. 2). Nearly half (45%) of the respondents
indicated that property damage had increased in the last 10 years, 46% of interviewees
had not noticed any changes in HEI trends, 8% had observed a decrease in
incidents and 3% of respondents did not answer the question. Similarly, 72% of respondents noted increased
crop raids, 21% did not notice any change and 6% indicated a decreasing trend.
A minority of respondents (22%) indicated an increase
in human casualties, 60% did not notice any change, and 10% indicated a
decreasing trend. More than 80% of
respondent could not provide information about elephant mortality in relation to
HEI, and only 10% indicated a decreasing trend in elephant casualties (Fig.
3). Most of the respondents (72%)
reported an increasing trend in crop raids over the past years. In summary, local perceptions indicated a
more significant increase in crop raids than in other types of damage (χ2=
95.0, df= 3, P= <0.001).
Crop type, damage incidence, and seasonal changes
Rice was the most common crop grown by 99% of the
interviewed households, followed by maize (79%) and wheat (43%). More than half (55%) of the households,
located predominantly to the south of the reserves, produced one crop of rice
per year, while 45% of the households, situated mainly to the north of the
reserves, produced two crops a year.
Only one crop of wheat and maize were grown per annum throughout the
buffer zones of both reserves.
Just over half
of the respondents (51%) indicated that elephants raided rice, over more than a
quarter of the respondents (34%) had witnessed elephants raiding maize
regularly, and 15% of respondents reported that wheat was a regular food choice
for raiding elephants. Most of the
respondents reported that the crop damage by elephants occurred in the
pre-monsoon and pre-winter seasons.
Forty-four percent of reports of HEI involving single
bulls or two bull elephants were of crop raids, 48% were of property damage and
8% were human casualties. Family herds
were found to raid crops (38%) and damage property (36%), but there were no
records of a human casualty caused by a family herd (25%).
There was significant correlation between the number
of crop raiding/property damage incidents and human casualties (r2=
0.8, P= <0.01). There was a
significant difference in the number of incidences of HEI relative to the time
of day, with almost 95% of all incidences occurring during the night
(18.00–02.00 h) (χ2= 108.30, df= 3, P= <0.001).
Plant parts preferred by elephants
Altogether 23% of interviewees described rice grain
with husks as the food most targeted by Asian elephants, followed by whole rice
plants without roots with 13% (χ2= 181.79, df=
2, p= <0.001). Twenty-eight percent
of the interviewees reported maize grain with husks as likely to be selected by
crop-raiding elephants (χ2= 274.89, df= 2,
p= <0.001). Eight percent of the
respondents reported that whole wheat plants without roots were also favoured,
and 7% described wheat grain with husks was also part of the raiding elephants’
diet while 21% of the respondents could not answer on preference for any of the
foods.
Incidents distribution by village
Overall, 55% of incidents were centred in southern and
southwestern parts of the park buffer zones.
Over half of the incidents (56%) occurred in the Chitwan National Park
buffer zone, and 44% occurred in the Parsa Wildlife
Reserve buffer zone. Ayodhyapuri
Village in Chitwan reflected the highest frequency of incidents (12%), followed
by Gardi Village (11%). In the Parsa
Wildlife Reserve buffer zone, Manahari Village
suffered the highest frequency of incidents (9.78%), followed by Nirmal Basti (8.0%).
There was significant negative correlation between the distance of a
village from park boundaries and the Incidences (r= –0.42, P= 0.02) (Fig. 4).
Regional trends
In the easternmost region, incidents per elephant was
1.74 (Fig. 5), and the number of human and elephant casualties was with 5.75
per annum (4.45 human casualties and 1.3 and elephant casualties). Human and elephant casualties were high
across all four known elephant distribution areas, however, the intensity of
casualty per elephant was only 0.06 as the number of elephants in this region
was the highest (around 100 individuals) within the four elephant distribution
regions in Nepal (Pradhan et al. 2011) (Fig. 5) at the time of this study.
In central Nepal (the Chitwan and Parsa
areas, Fig. 5), intensity of incidents was 1.53. The casualty per elephant (0.17) was highest
in this region (Fig. 5). The elephant
population was estimated at 25–30 individuals (DNPWC 2009; Pradhan et al. 2011)
and they are mostly residents.
Incident intensity excluding casualties was highest in
Bardia and Banke National
Parks in western Nepal (3.08), however, the rate of human and elephant
casualties per elephant was the lowest among all regions of the country (0.04)
(Fig. 5). The population was estimated
to be around 80 individuals in Bardia National Park
only (Pradhan et al. 2011).
In the far western region (Shuklaphanta
National Park and surrounding areas), the Asian Elephant population was low at
the time we conducted the research, with approximately 10 mixed migratory and
resident individuals (Velde 1997; Pradhan et al. 2011). Incident intensity per capita (i.e., per
elephant) was the lowest (0.19) among all the regions. Human casualties were low at the time of the
present study.
Minimising incidents
Of the questionnaire respondents, 46% of questionnaire
respondents reported a decrease in elephant abundance over the past 10 years,
while just under half (53%) of the participants reported an increase. Half of respondents were of the view that the
frequency of elephant visitations had been steady before five years, ranging
from one to three visits per year.
However, 47% of respondents thought that the frequency had increased
from only one to three to six visits per annum over the most recent 5-year
period, while 3% of respondents did not answer this question (Fig. 6).
When asked which of the given determinants they think
is the prime cause for the increased human-elephant incidents in this region,
many village residents (78%) identified the ineffective and inadequate elephant
deterrents such as trenches and electric fences as one of the causes of
increased HEI in the Chitwan-Parsa region. Half (50%) of the residents interviewed
believed that a higher number of elephants was the major cause of increased
problems (Fig. 7). The responses were
analyzed by categorized favour and disfavour proportions using z test of proportion. Parametric large sample z tests showed that
there were statistically significant differences between favour
and disfavour proportions
on ‘human moved into elephant habitat’ (z= -14.5, p <0.01), ‘changing
ranging behavior of elephants’ (z= -3.6, p <0.01) and ‘inadequacy of
preventive measures’ (z= 11.17, p <0.01) but responents
perceived the statistically equal proportion of favor and disfavour
proportions on increase in the number of elephants (z= 0.35, p >0.1). Overall, more respondents disfavoured
responses on the ‘human moved into elephant habitat’ and ‘changing ranging
behavior of elephants’, but they perceived the more favour
on inadequacy of preventive measures.
The proximity of agricultural lands to forest fringes
allowing easier access to elephants was regarded by 50% of respondents as being
the primary reason for elephants moving into human-occupied areas. A total of 45% of respondents believed that
depletion of natural wild foods in the forests resulted in elephants moving
into human habitats. An additional 5% of
respondents believed that human disturbance of elephant habitats was the cause
of elephants visiting villages in search of foods (χ2= 244, df= 13, p= <0.001)
Many of the respondents thought that food supply
should be a key focus in conflict mitigation: over half (53%) felt that the
regeneration of natural food plants in the forests would help reduce the
frequency of elephant visitations to cropped fields, and 40% were in favour of growing alternative crops and pursuing other
livelihoods. Six percent of respondents favoured translocation of problematic elephants to remote
areas and 1% of participants suggested culling repeat offenders.
In response to questions about how elephants could be
protected, 59% of the respondents were in favour of habitat
management inside parks, 33% supported raising people’s awareness about
elephant conservation and 32% suggested strong legal protection. A clear majority of local respondents (87%)
were positive about coexisting with elephants.
Responses about how human-elephant coexistence could be sustained in the
region included a 74% majority who favored a compensation program to replace
income lost to elephant damage. Over
half of the participants (56%) suggested electric fences as a way to reduce HEI
and to enhance peaceful coexistence.
Discussion
Our data showed that the scale of human-elephant
interactions differ according to the type of incident. Crop damage was the most common type of
incident. Of the most heavily cultivated
crops, rice was the most frequently raided.
Crop raiding by elephants is a major issue in many parts of Asia and is
caused by many factors, including elephant migration patterns, shifting water
resources, habitat depletion and seasonally dependent nutritional requirements
(Sukumar 1990). In our study area, rice
was cultivated twice per annum, and was the crop of choice for local
farmers. The primary reason for
elephants’ preference for rice could be related to the proximity of rice fields
to their seasonal migration routes (Neupane et al.
2017). In addition, our study has shown
that the spatial distribution of crop-raiding activity was not uniform in
either buffer zones of Chitwan or Parsa. Documented crop raids were mostly
concentrated in the southern buffer zone regions of the park areas, especially
in areas where cultivated crops were closer to park boundaries (Fig. 1). Therefore, proximity plays a vital role in
crop-raiding activity.
Elephant raids of rice during the grain producing
season (pre-winter) occurred more frequently than raiding of other crop
types. This may be due to nutritional
drivers. Our unpublished data shows
higher protein content in the grains of cereal crops compared to wild grass
species.
Elephants’ preferences for certain grain crops can be
explored further by identifying repeat raiders.
Most crop raids were by a single adolescent or a few bull elephants
identified by local villagers as repeat visitors that returned multiple times
over a period of several years. This
repeat crop-raiding behaviour could be correlated
with adult bulls having higher nutritional requirements than other elephants
because of their size and the high-energy behaviours
associated with the male drive for reproductive success (Sukumar & Gadgil 1988).
Our study also found that family herds ventured into
agricultural fields and caused damage.
This group behaviour could be predicted based
on changed migration patterns and home ranges (Pamo
& Tchamba
2001), as some of them have been found to visit new areas (Piple and Manahari VDC) in the
northern parts of the Parsa Wildlife Reserve and
Chitwan National Park where there had been no record of visitation by family
herds in the past. The changing behaviour of elephants could be triggered by resource
constraint in the area. The exploration
of new areas is likely to be due to habitat shrinkage, water depletion and the
increasing proximity of rice fields are consistent with elephant habitats. Such behaviour
change cannot be denied as there has been a recent report by Srinivasaiah et al. (2019) that young male elephants in
India, which are typically solitary, are now forming large male herds to
protect themselves from human retaliation. Our results showed that
elephant visitations have substantially increased in some areas during the last
five years, especially in the non-traditional migration regions.
The spatial distribution of village households and
their agricultural lands also played a crucial role in influencing HEI. Households in the forest fringe within
<5km of the periphery of national parks/reserves were more frequently
affected than more distant villages.
This was irrespective of their crop’s stage of growth, what type of crop
was cultivated or what type of property villagers held. A similar trend has been reported by Sukumar
(1990) in southern India and by Pant & Hockings (2013) in Nepal.
Interviewees’ perceptions of elephant conservation
were found to be unanimously positive in this study. People viewed natural food sources and
habitat restoration as the main areas to be addressed to achieve conservation
goals and to mitigate incidents.
Existing mitigation measures such as electric fences and traditional
herding techniques were seen to be least effective. The cultivation of elephant deterrent plants
in villages in the forest fringe was deemed not to be practical by surveyed
residents, as alternative income streams would be needed to replace the loss of
income from crops displaced by non-edible deterrent flora. Villagers suggested that night patrols during
peak crop-raiding times might not be feasible because of a lack of resources.
The spatial and temporal nature of incidents and
incidence intensity varied with region countrywide (Koirala et al. 2016). Our results indicated that eastern and western
regions were incident hotspots, while medium and lower incidence intensities
were typical in central and far western regions, respectively. The eastern region, which extends from Jhapa District in the far east through to Udaipur District
in the far western portion of the eastern-most quarter of the Asian Elephant’s
home range, was a critical conflict area.
The elephant population was as large as 100–115 individuals, mostly
migratory (DNPWC 2009; Pradhan et al. 2011).
In addition, incidence was high in this region in terms of elephant and
human casualties, but the intensity of damage per elephant was less than in
other regions because this region contained a higher number of migratory
elephants. The higher number of
casualties was attributed to the smaller area of forest-edge habitat (Nepal WWF
2007). There was also a higher probability of raids occurring whereever there was a longer perimeter of cultivated
habitat (Sukumar 1990). People in this
area grew a variety of crops. Some of
these were high-profit cash crops, and frequent elephant raids of such valuable
crops may have been intolerable to residents.
As a result, retaliatory killings of elephants and human casualties had
occurred. In contrast, in the western
region (Bardia and Banke
areas), the Asian Elephant population was estimated at ≤80 individuals at the
time of study, most of them migratory, with few permanent residents. Where elephants were fewer in number, human
casualties were less.
It was expected that this study would yield a detailed
account of crop and property damage caused by elephants in Nepal. Because the study period was short (just over
two years), comparing long-term trends was not possible. We expected that we would find that different
deterrents were used by locals in different regions, and that evaluations of
their effectiveness would lead to recommendations for novel damage mitigation
measures. We further expected to obtain
information about other mitigation measures from the literature and from other
parts of Nepal with similar HEI problems.
In addition, another of our goals was to understand
local people’s perception and attitudes towards the conservation of elephants,
in order to shed light on the scale of the problem and what measures would be
appropriate to introduce to reduce incidence in the future. Furthermore, information on the historic
distribution and threat status of Asian Elephants in Nepal would allow us to
draw conclusions on how the situation has changed over the past 10 years, and
which factors have contributed significantly to the current situation. Overall, results from this study were
expected to provide some basis for planners and conservationists to design
innovative approaches to reducing HEI in Nepal, because the dearth of
information available, makes conservation of the species extremely difficult.
In summary, our study suggests that in central Nepal,
the Asian Elephant population is increasing, and animals are mostly resident,
and the intensity of casualties was highest compared to other elephant
populations of the country. Crop raids
by elephants were the primary cause of HEI.
A combination of factors, including the depletion of natural food in the
forests, the higher nutritional content of crops and the proximity of rice
fields to elephant movement routes appeared to trigger crop raids, and HEI.
Based on our results, we have identified factors that
need to be assessed further to realise Asian Elephant
conservation outcomes and peaceful coexistence with humans. We recommend the following measures in the
form of an integrated approach to minimise incidence
and to conserve these endangered animals and their habitat for promotion of
peaceful coexistence.
1. Identify elephant refugia and migration routes and
assess the year-round availability and nutritional content of preferred food
plants in and around those areas.
2. Extension of effective electric fences in all major
agricultural areas of the buffer zones and consideration of digging elephant
deterrent trenches along remote park boundaries.
3. Introduce fair and workable compensation schemes to
address losses suffered from crop and property damage and to gain support from
local communities.
4. Restore degraded lands with a full suite of food
species preferred by elephants (Dharmaratne & Magedaragamage 2014) including bamboo, banana, and other
palatable plants.
Note: The most
widely used term ‘conflict’ was minimized and replaced with term ‘incident’,
‘competition’, and ‘coexistence’ (Davidar 2018).
References
Baidya, N.G., D.R. Bhuju & P.
Kandel (2009). Land use change in buffer zone of
chitwan national park, Nepal between 1978 and 1999. Ecoprint: An International Journal of Ecology
16: 79–86.
Chitwan National Park (2012). A Report on Problem Elephant submitted to Department
of National Park and Wildlife Conservation Submitted by Chitwan National Park,
Chitwan, Nepal.
Choudhury, A., D.K. Lahiri, Choudhury, A. Desai, J.W. Duckworth, P.S. Easa, A.J.T. Johnsingh & P.
Fernando (2008). “IUCN SSC Asian Elephant Specialist Group (2008).” Elephas
maximus. The IUCN Red List of Threatened Species (2008). T7140A12828813. https://doi.org/10.2305/IUCN.UK.2008.RLTS.T7140A12828813.en
Davidar, P. (2018). The term human-wildlife conflict creates more
problems than it resolves: better labels should be considered. Journal
of Threatened Taxa 10(8): 12082–12085. https://doi.org/10.11609/jott.4319.10.8.12082-12085
Dharmaratne, M.P.J. & P.C. Magedaragamage
(2014). Human elephant conflict and
solutions to it in Sri Lanka. Sciscitator 1:
56–58.
DNPWC (2009). The Elephant Conservation Action Plan for Nepal.
Ministry of Forest and Soil Conservation. Department of National Parks and
Wildlife Conservation, Kathmandu, Nepal, 38pp.
Hoare, R. (2000). African Elephants and humans in conflict: the outlook
for co-existence. Oryx 34(1): 34–38. https://doi.org/10.1046/j.1365-3008.2000.00092.x
Hoare, R.E. (1999). Determinants of human–elephant conflict in a land-use
mosaic. Applied Ecology 36: 689–700.
Joshi, R. & R. Singh (2007). Asian Elephants are losing their seasonal traditional
movement tracks: a decade of study in and around the Rajaji National Park,
India. Gajah 27: 15–26.
Kangwana, K. (1995). Human-elephant conflict: the challenge ahead.
Pachyderm (19): 11–14.
Koirala, R.K., W. Ji, A. Aryal, J. Rothman & D. Raubenheimer
(2016). Dispersal and ranging patterns of
the Asian Elephant (Elephas maximus) in relation to their interactions
with humans in Nepal. Ethology Ecology & Evolution 28(2):
221–231.
Kulkarni, J., P. Mehta, T. Pawar & R Mungikar (2010). Study on Human-Wild Animal Conflict around Chandoli National Park, Wildlife Research and Conservation
Society, Pune, India.
Nepal WWF (2007). A Case Study on Human-Wildlife Conflict in Nepal.
World Wide Fund, 64pp.
Pamo, E.T. & M.N. Tchamba
(2001). Elephants and vegetation change
in the Sahelo-Soudanian region of Cameroon. Journal
of Arid Environments 48: 243–253.
Pant, G. & M. Hockings (2013). Understanding the Nature and Extent of Human-Elephant
Conflict in Central Nepal. Masters research report, University of Queensland,
38pp.
Perera, B.M.A.O. (2009). The human-elephant conflict: A review of current
status and mitigation methods. Gajah 30: 41–52.
Pradhan, N.M.B. & P. Wegge (2007). Dry
season habitat selection by a recolonizing population of Asian Elephants (Elephas
maximus) in lowland Nepal. Acta Theriologica
52(2): 205–214.
Pradhan, N.M.B., A.C. Williams
& M. Dhakal (2011). Current status of Asian Elephants in Nepal. Gajah 35:
87–92.
Puyravaud, J.P., S. Gubbi, H.C. Poornesha
& P. Davidar (2019). Deforestation increases frequency of incidents with
elephants (Elephas maximus). Tropical Conservation Science 12:
https://doi.org/10.1177/1940082919865959
Riddle, H.S, B.A. Schulte, A.A
Desai & L. van der Meer (2010). Elephants- a conservation overview. Journal of
Threatened Taxa 2(1): 653–661. https://doi.org/10.11609/JoTT.o2024.653-61
Satyal, P.P. (2004). Country Profile Report-Forestry Sector in Nepal. Forests
Monitor, Cambridge, UK, 16pp.
Srinivasaiah,
N., V. Kumar, S. Vaidyanathan, R. Sukumar & A. Sinha (2019). All-Male
Groups in Asian Elephants: a novel, adaptive social strategy in increasingly
anthropogenic landscapes of southern India. Scientific Reports 9(1):
1–11.
Sukumar, R. (1989). The Asian Elephant: Ecology and Management. Cambridge
studies in applied ecology and resource management (USA), 244pp.
Sukumar, R. (1990). Ecology of the Asian elephant in southern India. II.
Feeding habits and crop raiding patterns. Journal of Tropical Ecology 6(1):
33–53.
Sukumar, R. (2003). The Living Elephants: Evolutionary Ecology,
Behavior, and Conservation. Oxford University Press, Oxford, UK, 477pp.
Sukumar, R. (2006). A brief review of the status, distribution and
biology of wild Asian Elephants Elephas maximus. International Zoo
Yearbook 40(1): 1–8.
Sukumar, R. & M. Gadgil (1988).
Male-female differences in foraging on crops by Asian Elephants. Animal Behaviour 36(4): 1233–1235.
Velde, P.F. (1997). A Status Report of Nepal’s Wild Elephant
Population. WWF Nepal. Kathmandu, 49pp.
Williams, C., S.K. Tiwari, V.R. Goswami, S. de Silva, A. Kumar, N. Baskaran, K. Yoganand & V. Menon (2020). Elephas maximus. The IUCN Red List
of Threatened Species 2020: e.T7140A45818198. Downloaded on 09 April
2021. https://doi.org/10.2305/IUCN.UK.2020-3.RLTS.T7140A45818198.en
Yadav, B. (2007). Human-elephant relationship and conflicts in eastern
Nepal. The Initiation 1: 93–99.