Deforestation and Fragmentation of Natural Forests in the Upper Changhua Watershed, Hainan, China: Implications for Biodiversity Conservation
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Environ Monit Assess (2015) 187:4137 DOI 10.1007/s10661-014-4137-3 Deforestation and fragmentation of natural forests in the upper Changhua watershed, Hainan, China: implications for biodiversity conservation De-Li Zhai & Charles H. Cannon & Zhi-Cong Dai & Cui-Ping Zhang & Jian-Chu Xu Received: 22 March 2014 /Accepted: 3 November 2014 # Springer International Publishing Switzerland 2014 Abstract Hainan, the largest tropical island in China, change were observed in protected areas, indicating a belongs to the Indo-Burma biodiversity hotspot. The lack of enforcement. Natural forests conversion to rub- Changhua watershed is a center of endemism for plants ber and pulp plantations has a general negative effect on and birds and the cradle of Hainan’s main rivers. How- biodiversity, primarily through habitat fragmentation. ever, this area has experienced recent and ongoing de- The fragmentation analysis showed that natural forests forestation and habitat fragmentation. To quantify hab- area was reduced and patch number increased, while itat loss and fragmentation of natural forests, as well as patch size and connectivity decreased. These land- the land-cover changes in the Changhua watershed, we cover changes threatened local biodiversity, espe- analyzed Landsat images obtained in 1988, 1995, and cially island endemic species. Both natural forests 2005. Land-cover dynamics analysis showed that natu- losses and fragmentation should be stopped by ral forests increased in area (97,909 to 104,023 ha) from strict enforcement to prevent further damage. Pre- 1988 to 1995 but decreased rapidly to 76,306 ha over serving the remaining natural forests and enforcing the next decade. Rubber plantations increased steadily the status of protected areas should be a manage- throughout the study period while pulp plantations rap- ment priority to maximize the watershed’sbiodi- idly expanded after 1995. Similar patterns of land cover versity conservation value. D.<L. Zhai (*) : J.<C. Xu C. H. Cannon Centre for Mountain Ecosystem Studies (CMES), Kunming Key Laboratory of Tropical Forest Ecology, Xishuangbanna Institute of Botany (CAS), Tropical Botanical Garden, Chinese Academy of Sciences, Lanhei Road132HeilongtanKunming 650201, China YunnanMenglun 666303, China e-mail: [email protected] e-mail: [email protected] J.<C. Xu e-mail: [email protected] D.<L. Zhai : J.<C. Xu World Agroforestry Centre (ICRAF), Central and East Asia C. H. Cannon Office, Department of Biological Sciences, Texas Tech University, Lanhei Road132HeilongtanKunming 650201, China Lubbock, TX, USA D.<L. Zhai : Z.<C. Dai Institute of Environment and Ecology, School of the Environment and Safety Engineering, Jiangsu University, C.<P. Zhang Xuefu Road 301, Zhenjiang 212013 Jiangsu, China Hainan Research Academy of Environmental Sciences, Z.<C. Dai Baiju Road 98, Haikou 571126, China e-mail: [email protected] e-mail: [email protected] 4137, Page 2 of 12 Environ Monit Assess (2015) 187:4137 Keywords Deforestation . Fragmentation . lack of clear understanding of the land-cover changes Connectivity. Plantation forest . Biodiversity and status of fragmentation makes it difficult for con- servation management practices to prevent further loss of habitat and biodiversity. Introduction In this study, we analyzed the spatial-temporal pat- terns of land cover and natural forests cover over three Tropical rainforests are seriously threatened by anthro- time points (1988, 1995, and 2005), using remote sens- pogenic forest degradation and deforestation (Laurance ing techniques, in the upper reaches of the Changhua 1999) which is resulting in a global biodiversity crisis watershed, Hainan, China. The objectives of this study (Anderson and Jenkins 2006). Tropical Asia is an im- were as follows: (1) to determine land-cover changes portant biodiversity hotspot (Myers et al. 2000). How- and associated habitat changes in the study area between ever, tropical Asia suffers serious forest loss and frag- 1988, 1995, and 2005; (2) to evaluate natural forests mentation due to land use and land cover changes, e.g., fragmentation using landscape indices; and (3) to dis- plantations displacing natural forests (Aziz et al. 2010; cuss the implications of these patterns for biodiversity Sodhi et al. 2010). Natural vegetation cover loss, forest conservation. fragmentation, and associated land-use and land-cover changes are the main processes causing global environ- mental change (Turner et al. 1995)andareresponsible Methods for the loss of biodiversity worldwide (Soule 1991;Sala et al. 2000). Forest fragmentation has become increasing Study area important for global change researches (Gibbs et al. 2010). It has been shown that land-cover analysis can Hainan Island (18° 10′–20° 10′ N and 108° 37′–111° 03′ discriminate specific habitat types and predict species E) (Fig. 1a) is the largest tropical island in China, with distribution at large spatial scales (Wang et al. 2010). an area of 33,920 km2. The island has a tropical mon- Therefore, although it is difficult to directly quantify soon climate, influenced by the southeast monsoon from biodiversity in a landscape, the sensitivity of biological the west Pacific Ocean and southwest monsoon from the communities to land-cover changes and the availability Indian Ocean in the summer and the northeast monsoon of appropriate habitat make it possible to project biodi- in winter, resulting in a rainy season from May to versity loss by land-cover conversion and habitat pa- October and a dry season from November to April rameters, derived from remote sensing studies. (Luo 1985). The annual mean temperature is 22–23 °C Hainan Island is the largest tropical island in China with 1800–2500 mm precipitation and 1800 mm evap- and the only major island in the Indo-Burma biodiver- oration annually (Luo 1985). The study area is the upper sity hotspot (Myers et al. 2000). The island includes two Changhua Watershed of Hainan Island (Fig. 1b), includ- of the World Wide Fund for Nature’s (WWF) Global ing parts of Wuzhishan National Nature Reserve (WZS) 200 ecoregions: the Hainan Monsoon Rain Forests and and Yinggeling Nature Reserve (YGL), with its eleva- the coastal plains, both of which are part of the extensive tion ranging from 169 to 1860 m above sea level South China-Vietnam Subtropical Evergreen Forests. (Fig. 1c). The interior uplands of the island are charac- Both its flora and fauna have high level of overall terized by great habitat diversity and are one of China’s diversity and endemism (Chan et al. 2005;Wangetal. most important biodiversity conservation areas (Feng 2006;Chen2008). Moreover, Hainan shares a strong et al. 1999; Francisco-Ortega et al. 2010). The historical and biotic connection with Southeast Asia, Changhua watershed is the cradle of Hainan’s main especially the Philippines and Malaysia, rather than rivers (Feng et al. 1999) and has been identified as a mainland China, indicated by the distribution patterns center of endemism for plants and birds (Wang et al. and genetic analysis of plants and animals (Su et al. 2006;Chen2008). 2007; Chen 2009;Dong2009; Chen and Sun 2010). Unfortunately, land-cover changes have already resulted Data sources and methods in substantial forest loss in Hainan (Zhang et al. 2000), which then can lead to the loss of biodiversity (Zhang Land-cover classification was performed using three et al. 2000, 2010;Lietal.2007; Cai et al. 2009). But the Landsat Thematic Mapper (TM) images and six Satellite Environ Monit Assess (2015) 187:4137 Page 3 of 12, 4137 Fig. 1 The Changhua watershed on the island of Hainan, China: a image of China showing the position of Hainan Island; b Hainan with the location of the study area indicated by black; c the upper reaches of Changhua watershed with the nature reserves Pour l’Observation de la Terre (SPOT 2) images for 2008), which has been preprocessed according to a three separate years: 1988, 1995, and 2005 (Table 1). standardized set of processing parameters (Landsat Sci- The TM and SPOT images of 1995 and 2005 were ence Team 2008), and orthorectified using geodetic and purchased from Beijing Spot Image Co., Ltd. and were elevation control data to correct for positional accuracy corrected for atmospheric and radiometric distortions. and relief displacement (Landsat Science team 2008). The Landsat TM image of the year 1988 was The data were topographically corrected through co- downloaded from USGS (Landsat Science Team registering them to a digital elevation model (DEM) (Ekstrand 1996), derived from topographic maps Table 1 Detailed information about the satellite images used in (scale=1:50,000) from the State Bureau of Surveying this study and Mapping. The orthorectified image matched well Acquisition date Sensor Path/row Spatial resolution (m) with the checked ground control points (GCPs) and their average root mean square error was less than a pixel 08 June 1988 TM4 124/47 28.5 which is 30 m×30 m. To enhance the image resolution, 28 December 1995 TM5 124/47 30 image fusion was made between multispectral TM and 15 January 1996 SPOT 2 278/311 10 the SPOT panchromatic band to produce a 10-m reso- 5 February 1996 SPOT 2 278/312 10 lution multispectral image. The image fusion was done 30 December 1995- SPOT 2 279/312 10 by principal component analysis (PCA) on PCI software 20 December 2005 TM5 124/47 30 (Chavez and Kwarteng 1989; Pohl and van Genderen 23 December 2005 SPOT 2 278/311 10 1998;Antunes2000). 23 December 2005 SPOT 2 278/312 10 Final images for each year were classified into six 7 November 2005 SPOT 2 279/312 10 land-cover types: (1) natural forests, 2) natural shrubs and grasslands, (3) tropical crops, (4) rubber plantations, 4137, Page 4 of 12 Environ Monit Assess (2015) 187:4137 (5) pulp plantations, and (6) open areas. “Natural for- the percentage of a class on the map that matches the ests” included primary forests and naturally corresponding class on the ground and measures the regenerating secondary forests, characterized by closed error of omission (1—user’s accuracy).