Proposed Extension of Public Golf Course at Kau Sai Chau, Sai Kung Environmental Impact Assessment Report Final Report

APPENDIX B ECOLOGICAL MONITOIRNG REPORT JULY 2004 TO JULY 2005

August 2005 Black & Veatch

Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ecological Monitoring Report: July 2004 to June 2005

Prepared for The Jockey Club Kau Sai Chau Public Golf Course Limited

Ecosystems Limited

July 2005

The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

TABLE OF CONTENTS

1 BACKGROUND 1

2 MANGROVE MONITORING 2 2.1 INTRODUCTION 2 2.2 MONITORING METHODS 2 2.2.1 Mangrove planting 2 2.2.2 Backshore vegetation 3 2.3 RESULTS 5 2.3.1 Mangrove survival 5 2.3.2 Growth 5 2.3.3 Reproduction 6 2.3.4 Backshore vegetation 6 2.4 CONCLUSIONS 7 2.5 RECOMMENDATIONS 8 3 AQUATIC FAUNA MONITORING 9

4 DRAGONFLY AND BUTTERFLY MONITORING 10 4.1 INTRODUCTION 10 4.2 MONITORING METHODS 10 4.3 RESULTS 10 4.3.1 Dragonflies 10 4.3.2 Butterflies 12 4.4 CONCLUSIONS 13 4.5 RECOMMENDATIONS 13 5 AMPHIBIAN & REPTILE MONITORING 14 5.1 INTRODUCTION 14 5.2 MONITORING METHODS 14 5.3 RESULTS 14 5.4 DISCUSSION 16 5.5 CONCLUSION 16 5.6 RECOMMENDATIONS 17 6 BIRD MONITORING 18 6.1 INTRODUCTION 18 6.2 MONITORING METHODS 18 6.3 RESULTS 20 6.3.1 Species Numbers 20 6.3.2 Bird Numbers 25 6.3.3 Dominance 26 6.3.4 Bird Species List 30 6.3.5 Incidental Observations 30 6.4 CONCLUSIONS 30 6.5 RECOMMENDATIONS 31 7 MAMMALS 35 7.1 BATS 35 7.2 PREDATION ON CIVETS BY FERAL DOGS 35 7.3 WILD BOAR 35 7.4 SUMMARY 36 7.5 CONCLUSIONS 37 7.6 RECOMMENDATIONS 37

Ecosystems Ltd. i The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

8 HABITAT MANAGEMENT 39 8.1 CORMORANT ISLAND 39 8.2 BAT ROOST BOXES 39 8.3 EGRETRY PLANTING 40 8.4 BIRD NEST BOXES 40 8.4.1 Introduction 40 8.4.2 Methods & Materials 41 8.4.3 Results 41 8.5 CONCLUSIONS 42 8.6 POTENTIAL HABITATS FOR SCHRENCK’S BITTERN ON KAU SAI CHAU GOLF COURSE 43 8.6.1 Introduction 43 8.6.2 Methods & Materials 43 8.6.3 Results 43 8.6.4 Recommendations 43 8.6.5 Recommendations 43 9 CONSERVATION EDUCATION 45 9.1 NATURE GALLERY 45 9.2 BIRD OF THE MONTH 45 9.3 FIELD TRIP & SEMINAR 45 10 REFERENCES 46

11 APPENDICES 47

LIST OF TABLES Table 2.1 Planting materials and methods and monitoring parameters below the main dam. Table 2.2 Percentage survival at Site E, March 2004 and May 2005, Kau Sai Chau. Table 2.3 Growth of seedlings at Site E, Kau Sai Chau, May 2005 Table 2.4 Plant species recorded on the backshore surrounding Site E, Kau Sai Chau, March 2004 and May 2005. Table 4.1 Dragonfly species recorded on northern Kau Sai Chau Golf pre-development (June 1994) and during ecological monitoring after construction. Table 4.2 Butterfly species recorded at Kau Sai Chau between July 1999 and June 2005. Table 5.1 Reptiles and amphibians recorded before and after construction of the golf course on Kau Sai Chau. Table 6.1 Dominant species and percent dominance for all sample sites over all sample periods at Kau Sai Chau between July 1995 and June 2005 Table 6.2 Bird species list for Kau Sai Chau showing local residence and breeding status; degree of global threat; listing under CITES; and protection status in China. Horizontal lines separate taxonomic families Table 7.1 List of dead civets recovered on Kau Sai Chau from May 1998 through 30 June 2005 Table 7.2 Mammals recorded on Kau Sai Chau from May 1993 through June 2005. Table 8.1 Locations of 10 bat roost boxes installed at Kau Sai Chau in December 2000.

Table 8.2 Bat box locations. Table 8.3 Average height of tree and bamboo species at egretry planting site Table 8.4 Nest box history Table 8.5 Contents of each nest box in spring 2005

Ecosystems Ltd. ii The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

LIST OF FIGURES Figure 2.1 Percentage Survival of Mangrove Seedlings at Site E from 1995 to 2005 Figure 2.2 Height of various mangrove species at Site E from 1995 to 2005 Figure 4.1 Cumulative number of dragonfly species recorded during 1995-2005. Figure 4.2 Cumulative number of butterfly species recorded during 1995-2005. Figure 5.1 Taxon accretion curve for reptiles and amphibians on Kau Sai Chau from 1993 to 30 June 2005 Figure 6.1a Locations of sampling transects and points of bird surveys Figure 6.1b Transect width in relation to centreline of transect Figure 6.2 Cumulative total number of species recorded during 10 years of sampling at Kau Sai Chau between summer 1995 and spring 2005 Figure 6.2a Species richness during summer for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005. Figure 6.2b Species richness during autumn for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005 Figure 6.2c Species richness during winter for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005 Figure 6.2d Species richness during spring for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005 Figure 6.3a Kau Sai Chau mean bird species counts by season from summer 1995 through spring 2005 Figure 6.3b Kau Sai Chau mean bird species count by year from 1995 through 2004 Figure 6.4 Means of four seasonal bird counts per year at Kau Sai Chau 1995-2005 Figure 6.5 Total bird counts by season during 40 sampling sessions at Kau Sai Chau from 1995 through 2004 Figure 6.6 Mean bird counts by year at Kau Sai Chau between 1995 and 2005 Figure 6.7 Number of sample seasons during which each of seven species was numerically dominant Figure 6.8 Mean annual dominance of the bird community from 1995-2005

LIST OF APPENDICES Appendix 1 Ecological Monitoring Schedule at Kau Sai Chau Golf Course, July 2004 to June 2005 Appendix 2a Mangrove planting site below the dam Appendix 2b Mangrove planting layout at Site E Appendix 3 Marbled Eel Anguilla marmorota captured in the pond east of North 2 green in spring 2005. Appendix 4 Chinese Cobra Naja atra Appendix 5 Egretry tree planting site Appendix 6 Marshes on Yim Tin Tsai & Kau Sai Chau Appendix 7 Nature Gallery display at clubhouse for conservation education Appendix 8a Visit to Wild Boar trap Appendix 8b Bird box checking Appendix 8c Slide show

Ecosystems Ltd. iii The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

Executive Summary Operational phase ecological monitoring of The Jockey Club Kau Sai Chau Public Golf Course Ltd. was initially performed from June 1995 to December 1998 to comply with requirements of the Environmental Impact Assessment (EIA) of the project. Monitoring resumed in July 1999 on an annual basis, and has continued through June 2005. This report covers the one-year period from 1 July 2004 through 30 June 2005. Monitoring to date has shown that construction and operation of the golf courses had the effect of virtually eliminating hillfires from the island, as predicted in the EIA. During the 10 years since the opening of the north course, habitats have begun to recover from previous fire damage, and many species of native flora and fauna are re-colonising the northern part of the island. Mangrove monitoring between 1995 and 2005 demonstrated that the mangrove restored below the reservoir dam has functioned successfully and as planned to mitigate the losses of mangroves in Kwat Tau Tam inlet. All mangrove plantations except the undisturbed Site C have survived. At Kwat Tau Tam mudflat elevations and substrate quality has enabled colonisation by species which were not planted. New mangrove seedlings have naturally colonised the created mudflats and new mangrove-associate vegetation has colonised the backshore zone. The mangrove Kandelia obovata had the highest rate of survival, natural colonisation, and growth. Many-petaled Mangrove Bruguiera gymnorrhiza seedlings survived when planted as droppers or as potted seedlings, while the mangrove Aegiceras corniculatum seedlings imported from Shenzhen had the lowest survival rate. K. obovata seedlings was recovered gradually from defoliation observed during the last sampling session. Avicennia marina, a dominant mangrove on the pre-construction mudflat, has colonised the created mudflat. Monitoring from July 1995 to June 2005 has shown an increase in numbers of wildlife species. Butterfly species increased by 3 from 25 to 28 during 2004-5. The pre-construction records of amphibians and reptiles included four species, as compared to the post-construction total of 18 species. No new amphibian or reptile species were added between July 2004 and June 2005. Eight snake species now occur on northern Kau Sai Chau, where none was recorded during EIA baseline studies. The bird species list increased from 132 to 135 during the year. No new mammal species were recorded and the total remained at 10. The increase in wildlife species and numbers is a positive trend and demonstrates that golf management has exerted a positive impact on the biodiversity of Kau Sai Chau. Wild Boar caused damage to golf course fairways, but no control action was called for during the year, and no boar were removed from the island. No native terrapin species has recorded on Kau Sai Chau between 1993 and 2005. A re-introduction programme of Reeves’ Terrapins is recommended. Colonisation of the golf course ponds and streams by reptiles and amphibians showed that golf course management practices did not adversely affect freshwater flora and fauna. The recovery of an adult Marbled Eel from the South 3 marsh supports that conclusion. Increased bird species numbers also documented progressive improvement in the quality or diversity of habitats on the island. Bat roost boxes installed in 2000 were occupied in 2004-5 and were monitored. Nine of 11 bird nest boxes were occupied during the spring 2005 breeding season. Collared Scops Owl nested in the box near North 2 tee in 2004 and 2005. A nesting habitat (egretry) for herons and egrets planted in April 2000 showed greatly improved growth of trees and bamboos. This was due to recycling of turfgrass clippings as compost at the egretry. One fatality of a Small Indian Civet was attributed to attacks by feral dogs during 2004-5. Feral dogs remain a nuisance and management challenge, although more than 10 dogs were captured and removed from the island. In summary, results of ecological monitoring during fiscal year 2004-5 confirmed that the golf course and its surroundings supported greater biodiversity than the previous land use.

Ecosystems Ltd. iv The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

1 BACKGROUND The Jockey Club Kau Sai Chau Public Golf Course Ltd. (hereafter Kau Sai Chau) opened its first 18 golf holes (the North Course) to the public on 27 December 1995, and the second 18 holes (the South Course) opened for play on 28 September 1996. The official opening was held on 13 November 1996. The EIA monitoring and audit requirements for the operational phase were detailed in the Environmental Monitoring and Audit (EM&A) Manual (July 1995), which covered EM&A requirements for the period June 1995 to December 1998. After the fulfilment of EM&A requirements in December 1998, Kau Sai Chau continued ecological monitoring from July 1999 through June 2003. The objectives of the ecological monitoring are: (1) to document changes in the restored mangroves and wildlife communities on and around the golf courses; and (2) to make management recommendations for enhancement of wildlife diversity and abundance, habitat quality, and mangrove restoration. The monitoring schedule is summarised in Appendix 1 and covers the following: • mangroves and backshore species below the dam; • butterflies and dragonflies; • amphibians and reptiles; • birds; and • mammals.

This report documents the results of the one-year monitoring period from 1 July 2004 to 30 June 2005 (the Kau Sai Chau Golf fiscal year). Cumulative results of monitoring since July 1995 are also discussed.

Ecosystems Ltd. 1 The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

2 MANGROVE MONITORING

2.1 Introduction Approximately 1.64 ha of mangroves were lost at Kwat Tau Tam inlet at the northern shore of Kau Sai Chau due to the construction of a reservoir for golf course irrigation. According to the Environmental Impact Assessment (EIA) report for the project, five sites (Sites A-E) on the island were selected for mangrove replanting to mitigate the loss. Of these, Site E was the primary planting site on the restored mudflat below the main dam at Kwat Tau Tam (Appendix 2a). Planting sites A to D were existing mudflats that were occupied by a few mangroves, and were selected for planting because of their potential to support larger or denser stands of mangroves. The mangrove planting layout at Site E is shown in Appendix 2b. Site E is divided by restored bunds into an upper site (immediately below the dam) and a lower site (furthest seaward). This yielded six monitoring sites in total (A to D, plus 2 sites at E). Planting materials and methods and monitoring parameters at this site are summarised in Table 2.1. Mitigation efforts included design, construction, planting, and monitoring of the created mangroves. More than 10,000 propagules (including droppers and seedlings) were collected or purchased, broadcasted or cultivated and planted during 1994-6 on all five sites. Initial trials of transplanting demonstrated that it was excessively labour-intensive and survival of transplanted trees was unacceptably low. Therefore transplantation was abandoned. Ecological monitoring was carried out to document the development and progress of mangrove rehabilitation at the six sites. Through December 1998, the overall survival rate at Sites A to D was 69%. Mangrove monitoring at Site C and part of Site B was abandoned due to poor survival. At the main planting site (Site E) below the dam, percentage survival stabilised for all mangrove species after an initial period of 4-5 years of fluctuation. Local Kandelia obovata seedlings had the highest survival rate, followed by local Bruguiera gymnorrhiza and then imported B. gymnorrhiza. Local K. obovata had the highest growth rate (1.2 cm/month), followed by imported B. gymnorrhiza and local B. gymnorrhiza. The current monitoring programme is the continuation of the operational phase ecological monitoring performed from June 1995 to December 1998. The purposes of the overall monitoring programme were to:

• monitor survival of mangrove propagules and seedlings; • quantify growth of mangrove propagules and seedlings; • monitor the natural recruitment of backshore vegetation; • monitor the colonisation and establishment of mangrove associated fauna; and • adjust the overall mangrove restoration strategy based on cumulative results.

Section 2.2 outlines the monitoring methods, while Section 2.3 summarises the results of monitoring. The succession of the mangrove community is described, and recommendations on maintenance and management are presented in Section 2.4.

2.2 Monitoring methods Monitoring methods followed as closely as possible those used during the EM&A period to enable comparison of results.

2.2.1 Mangrove planting

Ecosystems Ltd. 2 The Jockey Club Kau Sai Chau Public Golf Course Ltd. Ecological Monitoring Report July 2004 to June 2005

Three mangrove species, Kandelia obovata (formerly K. candel), Bruguiera gymnorrhiza, and Aegiceras corniculatum were planted/broadcasted during the planting stage. Selected clumps or individuals of these three species at Site E below the dam were sampled for survival and growth. Surveys were performed on 12 May 2005. Kandelia obovata propagule plantation Ten 1 m square plots were monitored. They were distributed to cover upper, middle and lower portions of the Kandelia obovata planting area in the seaward lagoon of Site E. Plants were counted and heights were measured for all individual plants within each plot. The total number of K. obovata at the lower lagoon in Site E was estimated to calculate percentage survival and/or growth. Bruguiera gymnorrhiza propagule plantation In the landward lagoon of Site E, 45 arbitrarily selected individuals of imported Bruguiera gymnorrhiza were monitored for growth rate and all plants were counted to assess percent survival. In the lower lagoon, 50 locally cultivated propagules were measured for growth rate and all plants were counted to quantify percent survival. Aegiceras corniculatum propagule plantation Aegiceras corniculatum propagules planted at the landward and seaward lagoons in Site E were counted for percent survival.

2.2.2 Backshore vegetation In prior reports six selected mangrove and mangrove associated species that colonised the backshore were counted. This procedure was discontinued in 2001-2 because most of these species colonised the backshore in large numbers, and natural recruitment was deemed successful. However, a cumulative species list was compiled to document the natural recolonisation process. Species established along the backshore, high tide area and bunds surrounding Site E were recorded.

Ecosystems Ltd. 3 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 2.1 Planting materials and methods and monitoring parameters below the main dam. Species Origin Propagules Number Planting method Planting Monitoring Sampling 1 planted date parameters method

K. c. local fruit 1000 direct seeding to a depth of 1/3- Jul 95 height4 10 1mx1m plots at lower (dropper) lower 1/2 the length of the droppers at lagoon 30 cm spacing 3500 Jul 96 survival count all at lower lagoon upper B. g. imported2 1 year old 469 removal of plastic bag and pit Aug 95 height 45 randomly selected seedling planting at 50 cm spacing plants survival all B. g. local 2-3 month- 130 removal of plastic bag and pit Aug 95 height 50 randomly selected old planting at 30 cm spacing plants cultivated seedling 3 survival all A. c. local fruit ca. 500 broadcasting Aug 95 - - A. c. imported2 1 year old 1256 removal of plastic bag and pit Aug 95 survival all seedling planting at 50 cm spacing L. r. local fruit ca. 500 broadcasting Aug 95 - - 1B.g. = K. c. - Kandelia obovata, Bruguiera gymnorrhiza, A. c. = Aegiceras corniculatum, L. r. = Lumnitzera racemosa. 2purchased from Neilingding Futian National Nature Reserve, Shenzhen, China. 3grown from field harvested propagules, planted into 5 cm diameter bags, and kept on site under a 50% shadecloth until they reached the 6-8 leaf-stage. 4Height of seedlings were measured from the upper tip of a dropper to the highest leaf nodes initially until after 20 months when such features

Ecosystems Ltd. 4 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

2.3 Results 2.3.1 Mangrove survival Summary results for mangrove survival at Site E during March 2004 and May 2005 are shown in Table 2.2 and Figure 2.1. Survival of the imported B. gymnorrhiza (E5 and Eabc) increased due to successful reproduction and establishment of seedlings. Many individuals were fruiting during the current survey. Many naturalised Bruguiera seedlings are indistinguishable from the imported seedlings. Survival of the home-grown B. gymnorrhiza (E2) reduced slightly. Survival rates of the imported A. corniculatum at E6 increased and decreased at E4 and local K. obovata increased slightly. Size of A. corniculatum however is still quite small with little growth observed over the years. Droppers and seedlings of Kandelia obovata and Bruguiera gymnorrhiza were still commonly seen on the mudflat, reflecting a rich seed source in the area.

Table 2.2 Percentage survival at Site E, March 2004 and May 2005, Kau Sai Chau. % Survival Number Surviving Mar 04 May 05 Mar 04 May 05 B. g. Imported E3abc Aug-95 323 144.3 164.1 466 530 B. g. Imported E5 Aug-95 146 49.3 52.1 72 76 B. g. KSC E2 Aug-95 130 56.9 49.2 74 64 A. c. Imported E4 Aug-95 793 8.1 6.2 64 49 A. c. Imported E6 Aug-95 463 4.5 5.8 21 27 K. c. HK E1,7,8 Jul-95 1000 150 156 1500 1560 *B.g. = Bruguiera gymnorrhiza, A.c. = Aegiceras corniculatum, K.c. = Kandelia obovata

Figure 2.1 Percentage Survival of Mangrove Seedlings at Site E from 1995 to 2005.

200

180

160

140

120 B.g (local) B.g (imported, ave) 100 K.c (local)

% survival 80 A.c. (imported, ave) 60

40

20

0 0 20406080100120 months after planting

2.3.2 Growth The local and home-grown B. gymnorrhiza and local K. obovata all grew slightly since the last monitoring period at March 2002 (Table 2.3, Figure 2.2) and showed a steady growth rate. K. obovata at the lower lagoon recovered gradually from last year’s poor growth. New

Ecosystems Ltd. 5 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

leaves and branches developed, and the Kandelia growth rate was higher than that of both local and home-grown B. gymnorrhiza. Avicennia marina naturally colonised the lower lagoon near the existing A. marina at Site E2. During the current monitoring session, the individuals were still in good condition.

Table 2.3 Growth of seedlings at Site E, Kau Sai Chau, May 2005 Species Origin Location Date Mean Height Growth Rate Planted (cm) (cm/month) Mar 04 May 05 Mar 04 May 05 B.g. Imported E3 Aug-95 119.80 123.2 0.32 0.24 B.g. KSC E2 Aug-95 97.18 99.14 0.29 0.18 K.c. HK E1 Jul-95 47.97 68.39 -0.97 1.86

Figure 2.2 Height of various mangrove species at Site E from 1995 to 2005.

140.0

120.0

100.0 imported Bruguiera 80.0 gymnorrhiza local Bruguiera 60.0 gymnorrrhiza height (cm) 40.0 local Kandelia candel 20.0

0.0 050100 months after planting

2.3.3 Reproduction Planted K. obovata and B. gymnorrhiza continue to produce droppers annually. A. corniculatum and A. marina have not yet produced droppers at Site E. L. racemosa trees that naturally colonized the backshore at Site E have produced droppers.

2.3.4 Backshore vegetation In April a total of 31 plant species was recorded along and above the high tide mark on the bunds surrounding Site E (Table 2.4). Plants recorded included mangroves, backshore species, common herbs, shrubs and trees. This indicates that a diverse backshore floral community is beginning to develop. Among these, Scaevola hainanensis (a locally rare backshore climber) and Heritiera littoralis (a locally rare mangrove) were last recorded in 1999. S. hainanensis was recorded during the current monitoring session recolonising the backshore of the landward lagoon near the imported B. gymnorrhiza plantation. Growth of invasive weeds (e.g. Conyza sp., Pueraria lobata, and Mikania micrantha) and aggressive climbers (Canavalia maritima) was not as vigorous as in previous years. Growth of invasive weeds (e.g. Conyza sp., Pueraria lobata, and Mikania micrantha) and aggressive climbers (Canavalia maritima) was less vigorous as in previous years. The backshore community reached a steady state in terms of species composition.

Ecosystems Ltd. 6 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 2.4 Plant species recorded on the backshore surrounding Site E, Kau Sai Chau, March 2004 and May 2005 Species Habit Exotic Mar-04 May-05 Aegiceras corniculatum S * Alyxia sinensis C * Apluda mutica G * * Blechnum orientale F * * Blumea sp. H * Breynia fruticosa S * * Canavalia maritima C * * Casuarina equisetifolia T E * * Clerodendrum inerme S * * Conyza sp. H E * Crotalaria mucronata H * Dicranopteris linearis F * Embelia laeta C * Eupatorium catarium H E * Excoecaria agallocha S * * Ficus superba T * * Fimbristylis spp. SE * Gossapinus malabaricum T E * Gynura bicolor H * Hibiscus tiliaceus T * Ipomoea brasiliensis C * * Ischaemum indicum G * * Lactuca indica H * * Leucaena leucocephala T E * * Limonium sinense H * Lumnitzera racemosa S * * Lygodium japonicum F * Macaranga tanarius T * Melastoma candidum S * * Melastoma sanguineum S * Miscanthus sp. G * * Nephrolepis cordifolia F * * Neyraudia reynaudiana G * * Paliurus ramosissimus T * Pandanus tectorius T * * Pityrogramma calmelanos F * Pteris ensiformis F * Pteris vittata F * * Pueraria lobata C * Rhaphiolepis indica S * Rhodomyrtus tomentosa S * * Rhus succedanea T * * Scaevola hainanensis C * * Scaevola sericea S * * Wedelia chinensis H * Wedelia triloba C E * * Wikstroemia indica S * Zoysia sp. G * * T = tree, S = shrub, H = herb, F = fern, C = climber, SE = sedge

2.4 Conclusions Survival rates of the mangrove seedlings have stabilised. Overall survival is good except for A. corniculatum and K. obovata at the upper lagoon of Site E.

Ecosystems Ltd. 7 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

The stable overall survival rate, the natural thinning taking place among the planted mangroves, the continued natural establishment of mangrove seedlings, and the flowering and fruiting of K. obovata and B. gymnorrhiza collectively indicate a self sustaining ecosystem has been restored and that further planting will not be required. Avicennia marina, a dominant mangrove species at Kwat Tau Tam inlet before golf construction, is recorded at Site E. A. marina is not commercially available, and natural colonisation is slow, both due to low fruit production and/or herbivory. Colonisation of Site E by A. marina indicates the suitability of the restored mudflat as a growth substrate. This is a positive sign for future establishment of the species.

Kandelia seedlings at lower lagoon started to recover from poor growth recorded in 2003-4, the previous monitoring session.

The development of the backshore floral community is considered to be successful overall in terms of natural recruitment and diversity of native species. Inventory of plant species will be continued to record new species colonising the backshore zone. Although invasive weeds, climbers and trees did not appear to cause serious problems during the current monitoring session, attention should be paid to the growth of these species and their effects on the backshore community.

2.5 Recommendations 1. The stand of Leucaena leucocephala below the reservoir dam should be destroyed. This is an aggressive exotic species that has potential to spread to other locations. 2. The single Casuarina equisetifolia tree below the reservoir dam should be destroyed. This is an exotic species that has potential to spread to other locations. 3. Efforts to eradicate Mikania micrantha on the golf courses and near the mangrove planting site have proven successful and should be continued. The greenskeepers have done an excellent job of manual removal of Mikania. Removal by uprooting prior to the winter flowering season is recommended. 4. Manual removal of the exotic Lantana camara has been successful. The greenskeepers have done an excellent job of removing stands of Lantana. Continued manual removal is recommended in spite of the fact that Lantana is an attractive food plant for butterflies. One suggestion is to advise the removal teams that only Lantana and not other species of shrub or tree are to be removed. 5. There are several Acacia confusa trees on the golf course. This is a naturalised exotic species that colonised the roughs after golf course construction (a few trees were planted during the construction phase). These trees should be removed whenever possible and ideally when they are small. The large A. confusa tree at the right side of North 10 and those near the pumphouse at the reservoir should be retained until they die naturally. The former supports a bird nest-box and the latter a natural nest.

Ecosystems Ltd. 8 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

3 AQUATIC FAUNA MONITORING Two species of aquatic fauna were discovered during maintenance projects at golf course ponds, one vertebrate and one invertebrate. The vertebrate was the Marbled Eel Anguilla marmorata that was discovered during spring 2005 in the stream/marsh/pond near the South 2 green (Appendix 3). Marbled Eel breeds in deep sea gullies where the young mature. Adult eels migrate to estuaries and rivers where they live in brackish or fresh water prior to reaching breeding age. Adults mature sexually when they descend rivers to reach the sea (Wang 1998). The maximum-recorded age is 40 years. Its survival in the marsh catchment on Kau Sai Chau is somewhat of a mystery. Several scenarios are presented below. 1. The eel recently migrated upstream from the sea. Movement of eels from the sea upstream to the marsh is blocked by a rock dam at the coast. The dam was built by farmers or fishermen and has been in place at least since 1979, according to a date inlaid in the dam in stone. The eel could not have reached the golf course from the sea by crossing this dam because it is too high (>4 meters). 2. The eel migrated inland before construction of the dam. The eel might have swum upstream from the sea prior to construction of the dam in 1979 (26 years ago). This might have been possible even though there would have been a steep incline from the sea to the stream (even at high tide). The eel would then have had to survive more that 26 years in the stream/marsh/pond, during which time farmers lived on the island and the golf course was constructed. During that time span the eel would not have returned to the sea because the dam presented too great a barrier. 3. The eel was released into the stream. Marbled Eel is considered a delicacy in local cuisine and is available in local fish markets. It is possible that the eel was released in the stream. This is unlikely for several reasons. First, Marbled Eel is not readily available in local markets. Second, only adult eels are typically offered for sale, and these are very expensive (>$1,000). Third, the stream on Kau Sai Chau is not a convenient or even likely habitat into which to release an eel for religious or other purposes. 4. The eel arrived after swimming overland during heavy rainfall when golf fairways were flooded. This is feasible because Marbled Eels can swim overland in very shallow water. However, the stream catchment where the eel was discovered is separated from adjacent catchments by relatively steep topography. The slopes leading to the catchment divide could not support enough water for the eel to swim up or breathe in. In addition, the adjacent catchments do not have streams that discharge to the sea via gentle gradients. Thus it is difficult to imagine how the eel might have even reached those catchments from the sea, to say nothing of how it might have migrated overland to the pond at South 2 green. The most likely of all these scenarios is number 2, in which the eel swam inland prior to construction of the dam in 1979 and survived in the stream since then. The second species of aquatic fauna discovered in 2004-5 was the Swan Mussel Anodonta woodiana. It was found during spring 2005 in Pond 11, the first pond upstream from the reservoir (C. Chan and C. Halliday, pers. comm.). More than 50 Swan Mussels were found around the pond edge when Pond 11 was part drained for clearance of aquatic weeds. Swan Mussel is one of a few freshwater mussels in Hong Kong. Its existence in the ponds on the golf course is somewhat of a mystery because there was little freshwater on the island prior to construction of the golf course. In the vicinity of the reservoir (Kwat Tau Tam Inlet) there was no freshwater except surface runoff in gullies during heavy rains. Larvae of the Swan Mussel are parasitic on the gills and fins of fish for 10-14 days before dropping of to become free-living mussels (Dudgeon and Corlett 1994). Fish are abundant in all of the ponds and the reservoir so reproduction is not limited by availability of hosts. Swan Mussels are filter feeders, presumably finding an abundant food resource in the plankton of the ponds and reservoirs.

Ecosystems Ltd. 9 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

4 DRAGONFLY AND BUTTERFLY MONITORING

4.1 Introduction Ecological monitoring was carried out between July 2004 and July 2005 to document the dragonfly and butterfly species on and around the golf centre. The purpose of the monitoring was to document the development of the dragonfly and butterfly communities. Dragonflies are considered to be useful bio-indicators of the quality of freshwater habitats: areas that support breeding populations of some dragonflies are typically high quality habitats, and the presence of dragonfly nymphs is dependent upon good water quality (Wilson 1995). Adult dragonflies also hunt near aquatic habitats. Species richness of dragonflies may be used to assess habitat diversity in an area (ibid.). Similarly, butterflies are often considered a bio-indicator of upland habitat quality. Diversity of butterflies in an area is related to the availability of food plants, which are mainly flowing plants that produce nectar or fruits.

4.2 Monitoring methods Qualitative surveys for dragonflies and butterflies were carried out on 1 and 14 April 2005. Dragonflies and butterflies encountered were identified to species. Taxonomy of dragonflies follows Wilson (2003) and taxonomy of butterflies follows Yiu (2004).

4.3 Results 4.3.1 Dragonflies No new dragonfly species was added to the list since 2001. This may be due to the fact that possible ecological niches on the golf course have been filled. Thirty-seven dragonfly species (Table 4.1), representing 33% of the 111 species in Hong Kong (Wilson 2003), were recorded on Kau Sai Chau during the operational phase ecological monitoring that began in July 1995 (Figure 4.1).

Figure 4.1 Cumulative number of dragonfly species recorded during 1995-2005.

40

30

20 No. of species

10

0 1995 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 Year

Ecosystems Ltd. 10 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 4.1 Dragonfly species recorded on northern Kau Sai Chau Golf pre-development (June 1994) and during ecological monitoring after construction Year first recorded after completion of Order, Family Scientific Name Jun golf course Commonness 1994 construction in Hong Kong Zygoptera, Coenagrionidae Orange-tailed Midget Agriocnemis femina Jun 2000 A Marsh Dancer Onychargia atrocyana + Oct 1995 UC Common Bluetail Ischnura senegalensis + Jul 1996 A Orange-tailed Sprite Ceriagrion auranticum + Jul 1996 A Brook Sprite Pseudagrion spenci Mar 1998 R Blue Sprite Pseudagrion microcephalum Mar 1998 UC

Zygoptera, Platycnemididae Blue Forest Damsel Coeliccia cyanomelas + A Black-kneed Featherlegs Copera ciliata + Jul 1996 A Yellow Featherlegs Copera marginipes + Jul 1996 A

Zygoptera, Protoneuridae Black threadtail Prodasineura autumnalis + Jun 2001 A

Anisoptera, Aeshnidae Common Evening Hawker Anaciaeschna jaspidea Jul 1997 UC Lesser Emperor Anax parthenope Jun 2000 C Pale-spotted Emperor Anax guttatus Jul 1996 A

Anisoptera, Gomphidae Common Flangetail Ictinogomphus pertinax + Oct 1995 A

Anisoptera, Libellulidae Blue Dasher Brachydiplax chalybea + Mar 1998 C Scarlet Dwarf Nannophya pygmaea + Oct 1995 UC Red-faced Skimmer Orthetrum chrysis + Jul 1996 C Common Blue Skimmer Orthetrum glaucum + Jul 1996 A Marsh Skimmer Orthetrum luzonicum + Jul 1996 A Common Red Skimmer Orthetrum pruinosum + Jul 1996 A Green Skimmer Orthetrum sabina + Jul 1996 C Asian Pintail Acisoma panorpoides + Jun 2000 C Asian Amberwing Brachythemis contaminata Jul 1996 A Crimson Darter Crocothemis servilia Jul 1997 A Blue Percher Diplacodes trivialis Jun 2000 A Pied Percher Neurothemis tullia + Oct 1995 C Russet Percher Neurothemis fulvia Jul 1996 A Pied Skimmer Pseudothemis zonata Jun 2001 C Crimson Dropwing Trithemis aurora + Jul 1996 A Indigo Dropwing Trithemis festiva + Mar 1998 A Dancing Dropwing Trithemis pallidinervis Oct 1999 R Wandering Glider Pantala flavescens + Oct 1995 A Variegated Flutterer Rhyothemis variegata + Jul 1996 C Sapphire Flutterer Rhyothemis triangularis + Oct 1995 UC Evening Skimmer Tholymis tillarga Oct 1995 C Saddlebag Glider Tramea virginia + Jul 1996 C Scarlet Basker Urothemis signata Mar 1998 C Emerald Cascader Zygonyx iris Oct 1995 A Total number of species 23 37 Commonness: A = abundant, C = common, FC =fairly common, UC = uncommon, R =rare

Ecosystems Ltd. 11 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

4.3.2 Butterflies Three new butterfly species were recorded between July 2004 and June 2005 (Table 4.2). These were Common Palmfly Elymnias hypermnestra, Common Five-ring Ypthima baldus and Straight Five-ring Y. lisandra. All are common/very common in Hong Kong (Yiu 2004). A total of 28 species have been recorded since July 1999, representing 11.7% of the 230 species in Hong Kong (ibid.). The number of butterfly species continues to increase annually (Fig 4.2).

Table 4.2 Butterfly species recorded at Kau Sai Chau between July 1999 and June 2005. Common name Latin name 99– 00– 01– 02– 03– 04– Commonness 00 01 02 03 04 05 Large Faun Faunis eumeus + + VC Common Tiger Danaus genutia + + + + VC Blue-spotted Tiger Euploea midamus + VC Blue Tiger Tirumala limniace + + + C Glassy Tiger Parantica aglea + + VC Bush Hopper Ampittia dioscorides + UC Purple Sapphire Heliophorus epicles + C Tailed Cupid Everes lacturnus + C Pale Grass Blue Zizeerie maha + + VC Common Lascar Pantoporia hordonia + C Red Ring Skirt Hestina assimilis + C Great Eggfly Hypolimnas bolina + + + + C Peacock Pansy Junonia almana + + + C Short-banded Sailor Phaedyma columella + C Angled Castor Ariadne ariadne + + + C Plum Judy Abisara echerius + + VC Punchinello Zemeros flegyas + + + + + C Paris Peacock Papilio paris + + + + VC Red Helen Papilio helenus + + + + + VC Common Mormon Papilio polytes + + + + + + VC Great Mormon Papilio memnon + + + C Common Bluebottle Graphium sarpedon + + + VC Indian Cabbage White Pieris canidia + + + + + VC Mottle Emigrant Catopsilia pyranthe + C Common Grass Yellow Eurema hecabe + + + + + + VC Red-base Jezebel Delias pasithoe + + + + VC Common Palmfly Elymnias + C hypermnestra Banded Tree Brown Lethe confusa + VC Dark Brand Bush Mycalesis mineus + + VC Brown Common Five-ring Ypthima baldus + VC Straight Five-ring Ypthima lisandra + VC

Total number of 14 16 14 11 12 13 species Commonness: C = common, UC = uncommon, VC = very common (Yiu 2004)

Ecosystems Ltd. 12 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 4.2 Cumulative number of butterfly species recorded during 1995-2005.

30

25

20

15 No. of species 10

5

0 1993 1994 1995 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005

Year

4.4 Conclusions 1. No new dragonfly species has been recorded since 2001, this may be because ecological niches for dragonfly on the golf course have been filled. 2. Three new species of butterfly was recorded between July 2004 and June 2005. However, the total species richness of butterflies on the golf course remained low. This is probably related to the vegetation cover, which consisted mainly of sparse shrubs and open areas. With continued hillfire suppression tree cover will progressively increase. Shrublands will slowly become woodlands and the numbers of flowering plants will increase. This will foster continued growth in the number of butterfly species on the island.

4.5 Recommendations The diversity of butterfly on Kau Sai Chau may depend on vegetation cover and plant diversity. One way to enhance butterfly diversity on the golf course will be the control or eradication of the exotic climber Mikania spp. and planting the larval food plants of some target species. The presence of larval food plants is an important factor determining the presence of a butterfly species in an area. For example, the planting of Indian Birthwort Aristolochia tagala, a foodplant of the protected species Common Birdwing Troides helena and Golden Birdwing T. aeacus, in Kadoorie Farm & Botanic Garden, Shan Liu and Tai Po Kau Nature Reserve to conserve/enhance the population of Common Birdwing Troides helena has been fairly successful (Young and Reels 1998). The diversity of the butterfly community on Kau Sai Chau could be enhanced by planting these and other larval food plants.

Ecosystems Ltd. 13 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

5 AMPHIBIAN & REPTILE MONITORING

5.1 Introduction Frogs are useful indicators of the quality of freshwater habitats because frogs require freshwater during all phases of their life cycle. They lay eggs in or near freshwater, eggs hatch to tadpoles that live entirely in freshwater, and tadpoles mature to adult frogs that feed and breed in freshwater. Certain physiological traits (e.g. permeable skin), together with the biphasic life cycle, make frogs potentially excellent indicators of habitat quality. Toads are less dependent on freshwater, as are most snakes and geckos. Amphibians and reptiles are functionally important in most freshwater habitats. The diets of frogs, toads and reptiles are all related to freshwater productivity. Frogs and toads, for example, eat insects and other aquatic invertebrates, snakes eat invertebrates, frogs, toads, other snakes, birds, and rodents. Apart from being herbivorous, terrapins may also act as scavengers. The increased area of freshwater ponds on Kau Sai Chau has greatly increased the area of suitable habitat for frogs and toads on the golf courses. The result has been an increase in species numbers and population numbers for most species. Reptile numbers and species have also increased, probably in part due to the increase in available amphibian prey.

5.2 Monitoring methods Night surveys of amphibians and reptiles were carried out on 1 and 14 April 2005. Active searches for reptiles and amphibians were conducted in representative habitats. Frogs were identified by sight and vocalisation. Records kept by the greenskeeping staff are also included in this report. Nomenclature used in this report for reptiles follows Karsen et al. (1998) while that for amphibians follows Lau and Dudgeon (1999).

5.3 Results Signs of Burmese Python Python molurus on fairway were reported by personnel in 2005. Tracks of Python on the golf course were first reported in 2000. Burmese Python, though a forest dweller, can occur in many types of habitats. It is reported from widespread localities in Hong Kong, and this may be partly related to its ability to swim. This is a State Class 1 Protected Animal of China (Zhao 1998). A second snake, Chinese Cobra Naja atra, was sighted at the dam of the reservoir on 14 April 2005 (Appendix 4). Three-banded Box Terrapins Cuora trifasciata were reported by personnel. This is a very rare forest stream terrapin in Hong Kong (Karsen et al. 1998). Three-banded Box Terrapin is a State Class 2 Protected animal in China, and its abundance has declined sharply due to over-harvesting for medical uses and as food (Zhao 1998). The only terrapin species recorded on the golf course/the island during ecological monitoring surveys, and surveys for the EIA of the existing and proposed third golf course is Red-eared Slider Trachemys scripta. Red-eared Sliders are present in the ponds on the golf course and streams of the rest of the island. No native terrapin species has been recorded on Kau Sai Chau over the last 12 years. Terrapins are common fauna in aquatic habitats, but their abundance has declined due to over-exploitation. During the night surveys on 1 and 15 April 2005, few frogs were heard except in the water intake locations on the fairways. These were Gunther’s Frog Rana guentheri and Asian Common Toad Bufo melanostictus. The presence of tadpoles in the ponds, however, showed that breeding still occurred. Reptile and amphibian species recorded over ten years of golf operation is shown in Table 5.1. & Figure 5.1.

Ecosystems Ltd. 14 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 5.1 Reptiles and amphibians recorded before and after construction of the golf course on Kau Sai Chau. Pre-Construction - May 1993 to May 1994 Class, Order, Family Common Name Scientific Name Year Recorded Amphibia, Anura, Ranidae Günther’s Frog Rana guentheri 1993 Three-striped Grass Rana macrodactyla 1993 Frog Reptilia, Squamata, Bowring’s Gecko Hemidactylus bowringii 1993 Gekkonidae Garnot’s Gecko Hemidactylus garnotii 1993 Post-Construction - July 1995 to present Class, Order, Family Common Name Scientific Name Year First Recorded Amphibia, Anura, Bufonidae Asian Common Toad Bufo melanostictus 1995 Amphibia, Anura, Ranidae Günther’s Frog Rana guentheri 1995 Two-striped Grass Rana taipehensis 2001 Frog Three-striped Grass Rana macrodactyla 2002 Frog Amphibia, Anura, Brown Tree Frog Polypedates 1996 Rhacophoriidae megacephalus Amphibia, Anura, Microhylidae Asiatic Painted Frog Kaloula pulchra 2002 Reptilia, Testudinae, Red-eared Slider Trachemys scripta elegans 1997 Emydidae Reptilia, Squamata, Bowring’s Gecko Hemidactylus bowringii 1995 Gekkonidae Garnot’s Gecko Hemidactylus garnotii 1995 Reptilia, Squamata, Grass Lizard Takydromus sexlineatus 2002 Lactertidae Reptilia, Squamata, Boidae Burmese Python Python molurus bivittatus 2000 Reptilia, Squamata, Buff-striped Keelback Amphiesma stolatum 2003 Colubridae Large-spotted Cat Boiga multomaculata 2001 Snake Copperhead Racer Elaphe radiata 1998 Indo-Chinese Rat Ptyas korros 1995 Snake Reptilia, Squamata, Elaphidae Chinese Cobra Naja atra 1999 King Cobra Ophiophagus hannah 2001 Reptilia, Squamata, Viperidae Bamboo Snake Trimeresurus albolabris 1996

Ecosystems Ltd. 15 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 5.1 Species richness for reptiles and amphibians on Kau Sai Chau from 1993 through June 2005

20

15

10 No. of species

5

0 1993 1994 1995 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 Year

5.4 Discussion During night surveys between 2001 and 2004, many frogs were seen and heard. However, few frogs were heard during the surveys in 2005. The apparent decline in amphibian abundance may be related to the recent clearance of aquatic weeds within some golf course ponds. Grasses provide shelter or escape cover for frogs, and may determine their abundance on the golf course. Frogs can probably only inhabit the pond shores due to the presence of predatory fishes in deeper waters of the pond. Where the vegetation cover within ponds was reduced, frog abundance appears to have fallen. This impact will be of relatively short duration at Pond 1 because the vegetation removal project in 2005 was intended to restore the pond to a condition similar to that found in the late 1990s. Aquatic vegetation will begin again to colonise the pond and the shoreline vegetation will grow back. This will progressively improve habitat quality for frogs.

5.5 Conclusion The apparent decline in amphibian numbers on the golf course in 2005 will probably be of short duration. It resulted from pond restoration projects that are now completed. Aquatic and shoreline vegetation that provides shelter or escape cover for frogs will quickly become re-established. Reptile species recorded on Kau Sai Chau over the last 12 years included only skinks, lizards and snakes but no native terrapin species. The absence of native terrapins, which should be common in aquatic habitats, is due to long-term exploitation (human colonisation in Kau Sai Chau might have begun as early as 1300 A.D.). Terrapins are slow moving animals and are not venomous (as are some snakes), and so are easy preys for humans. Kau Sai Chau is an island and re-colonisation of the restored habitats by freshwater terrapins has been impossible without human assistance. The successful establishment of the Red-eared Slider demonstrates the availability of terrapin niches on the golf course and the rest of the island.

Ecosystems Ltd. 16 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

5.6 Recommendations 1. Maintenance of a buffer of unmown vegetation of about 5 m on the bank of each of the ponds adds to the value of the ponds by increasing the area and quality of foraging, breeding, and escape cover. Such buffers should be maintained where they do not interfere with golf play. 2. Release of Reeves’ Terrapin . Reeves’ Terrapin Chinemys reevesii was once Hong Kong’s most common turtle and is still considered common now. It is found throughout Hong Kong, including some of the smaller islands, e.g., Cheung Chau and Peng Chau. Since Kau Sai Chau is the fifth largest island in Hong Kong and lies near the mainland of Sai Kung Peninsula, it is likely that this species once occurred on Kau Sai Chau. It feed on fishes, frogs, carrion and vegetation. Abundance of Reeves’ Terrapin in Hong Kong and throughout China declined greatly due to harvesting for food consumption and medical uses. We propose a preliminary release of 10 individuals: 5 males & 5 females into the marsh near North 15. Reasons of the proposal of this release program are: a) this species probably once occurred on Kau Sai Chau. It may have been eliminated by overexploitation by villagers (which may have continued for centuries) and habitat degradation. This program will aim to reintroduce this species to Kau Sai Chau, since Reeves’ Terrapin cannot re-colonize the restored/created wetland habitats on the island by itself; b) Terrapins are common elements in aquatic habitats throughout the world. There may be a vacant niche at Kau Sai Chau for a carnivorous and amphibious animal. Reintroduction of this species to the marsh would increase indigenous biodiversity in the aquatic ecosystem; c) This reintroduction program may also assist the establishment of a population (hopefully a self-sustaining one) at a site relatively safe from illegal trapping (which is pervasive in Hong Kong); d) In order to ensure the success of this re-introduction program, a scheme to remove the exotic Red-eared Slider may be proposed later. In Hong Kong, naturalists believe this species largely replaces Reeves’ Terrapin in the wild.

Ecosystems Ltd. 17 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

6 BIRD MONITORING

6.1 Introduction Bird surveys were conducted to quantify species presence, bird abundance, and changes in those parameters over time. Survey results enable comparison of bird species and population numbers over time. Like amphibians, many birds rely on invertebrate prey captured on the golf courses. Therefore birds, particularly residents or summer visitors (breeding birds) are good indicators of the overall ecological health of the golf course. Birds that migrate through Hong Kong and those that stay seasonally are also indicators but they are less reliable because their population numbers may be influenced by factors on their breeding ranges or migratory routes. Birds at Kau Sai Chau have been monitored by the same observer using the same sampling stations and methods for 10 years. Birds have been sampled on 4 transects and 3 point stations 4 times quarterly, twice just after sunrise and twice just before sunset. All sampling locations but one have been surveyed 160 times (the other 156 times). This is one of the longest bird monitoring studies ever carried out in Hong Kong. The consultant knows of no other golf course in the world that has carried out a study of birds of this intensity and/or duration.

6.2 Monitoring methods Birds were counted quarterly each year from summer 1995 through spring 2005 on 4 belt- transects and 3 point-count stations (Figure 6.1a). Sampling in 2004-5 was carried out in July and October 2004, and January and April 2005. Morning sampling started at sunrise, and evening sampling was conducted during the last hours of daylight until dusk. Sampling required 2.5-3 hours to complete all transects and point counts. Each of the 7 sampling sites was sampled 4 times quarterly, twice in the morning, and twice in the evening following recommendations of Moskat and Baldi (1993). The order of sampling on all occasions was: Transect 4 (T4), Point 3 (P3), Transect 4 (T4), Transect 8 (T8), Point 10 (P10), Point 13 (P13), and Transect 30 (T30). Transect 8 was interrupted midway through the transect to sample Point 10. Transects and point counts were numbered to correspond to the golf holes where the transect started.

Ecosystems Ltd. 18 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.1a Locations of sampling transects and points

Belt-transects were 100 m wide, 50 m either side of the edge of the fairway. Birds were counted in a belt covering equal-width strips of golf fairway and adjacent natural habitat. Transects measured 1 km in length. Each transect required 25-30 minutes to sample, depending on the number of birds recorded. Points were sampled without boundaries over a 10-minute sample period which followed immediately after a 5-minute settling period when the observer remained still at the point count site. Birds recorded were identified to species where possible, counted, their habitat use was recorded, and their perpendicular distances from transect centre lines or radial distances from points were recorded (Figure 6.1b). Birds were recorded visually and aurally. Sampling methodology followed Burnham et al. (1980) for belt transects and Reynolds et al. (1980) for point counts.

Ecosystems Ltd. 19 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.1b Transect width in relation to centreline of transect

This report includes results from 40 sampling sessions over 10 years, or 160 sample runs over each of the 7 sampling sites except for Point P13, which was sampled 156 times. P13 was not sampled during the first sampling session in July 1995 because construction works had not yet been completed on the site. Transects T24 and T4 sampled native coastal and upland shrub habitats and adjacent fairways. Transects T8 and T30 sampled disturbed (by hill fire or golf course construction) coastal and upland habitats and fairways. Point count sites sampled golf course and native coastal habitats (P3); upland habitats affected by golf course construction and fire, golf course, and fresh water ponds (P10); and a mangrove plantation together with native coastal habitats (P13). Dominance was calculated using the Berger-Parker index d (Berger and Parker 1970, in Magurran 1988) which expresses the proportional importance of the single most abundant species

d = Nmax / N

where Nmax = the number of individuals in the single most abundant species, and N is the sample total count. Single-factor and two-factor ANOVA were used to test the null hypotheses that mean bird abundance and species richness were similar between sample sites or habitats and within site types (points or transects). The Tukey test (Zar 1984) was then used to determine the significance of differences between transect results. Unless otherwise stated in the text, a significance level of α = 0.05 was used for all comparisons. The Tukey Test calculation procedure for standard error was modified following Kramer (1956, in Zar 1984) to account for unequal group sample sizes in point count comparisons involving point site P13, which was not sampled in July 1995. Paired t-tests were used in comparisons of numbers of birds recorded in morning versus afternoon sampling sessions. All statistical tests were undertaken using Statistix 7© and Microsoft Excel© software.

6.3 Results 6.3.1 Species Numbers 135 species of birds were recorded on Kau Sai Chau during the 10-year study period. 120 species were recorded during transect and point count sampling, and 15 additional species were recorded on other areas of the island (Figure 6.2). The total represents 30% of the 450 bird species recorded in Hong Kong over the last 50 years. Two species were added to

Ecosystems Ltd. 20 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

the cumulative total during sampling in 2004-5. These were: Eurasian Wryneck and Hwamei. Both were recorded during autumn (8-9 October 2004). Eurasian Wryneck is a migratory woodpecker, a winter visitor to Hong Kong. Hwamei is a resident laughing thrush. The increase in recorded bird species over the last ten years is shown in Figure 6.2.

Figure 6.2 Cumulative total number of species recorded during 10 years of sampling at Kau Sai Chau between summer 1995 and spring 2005

160 140 120 100 80 60

number of species 40 20 0

7 9 0 0 3 4 95 96 6-7 9 0 01 02 0 0 05 Su Sp 9 A9 Su98 Sp 9-0 A Su Sp Au Su Sp W 9 W02-3 W

Combined Total

The continued increase in species numbers is due to improved quality and diversity of habitats following completion of the golf courses. One key factor is the freshwater ponds and reservoir, neither of which occurred on Kau Sai Chau prior to 1994. Many of the waterbirds now found on the island inhabit these new freshwater wetlands. A second important factor is elimination of hillfire as an agent of habitat destruction. This results from the firebreak effect of the golf course. Prior to 1994 hillfires that began at gravesites on the northeast headland of the island swept across the island destroying shrub and tree seedlings, and holding the vegetation in an unnatural grassland-shrubland stage (a plagioclimax or fire-disclimax). After 1995 fires have been virtually eliminated from the golf course and all areas to the south. As a result the vegetation in natural shrubland and woodland habitats in and around the golf courses has progressively become more dense. Trees are more abundant, and both trees and shrubs have grown taller. Eurasian Wryneck, first recorded in 2004-5, was seen in maturing trees near the North 13 tee (one bird was recorded). Hwamei was recorded in maturing shrubland near North 6. The numbers of bird species recorded in each year are shown by season in Figures 6.2a-d. Numbers of new species recorded during each year are also shown. The summer 2004 species total of 24 was the lowest summer count on record. Similarly, the winter 2004-5 count of 34 species was also the lowest winter count on record. Autumn 2004 and spring 2005 counts were at or near the median for those seasons.

Ecosystems Ltd. 21 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.2a Species richness during summer for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005.

40 35 30 25 Total Species Count 20 No. of New Species 15 10 Number of species 5 0 12345678910 Year

Figure 6.2b Species richness during autumn for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005

60

50

40 Total Species Count 30 No. of New Species 20 No. ofspecies

10

0 12345678910 Year

Figure 6.2c Species richness during winter for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005

50 45 40 35 30 Total per year 25 No. of New Species 20

No. of species 15 10 5 0 12345678910 Year

Ecosystems Ltd. 22 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.2d Species richness during spring for combined transect and point count sampling at Kau Sai Chau between 1995 and 2005

60 50 40 Total Species Count 30 No. of New Species 20 10 Number of species Number of 0 12345678910 Year of monitoring

Species totals differed significantly by season (F=13.8, P<0.001, df=36) (Figure 6.3a). The mean summer species count was significantly lower than the means for spring (Tukey’s T=7.7, P<0.01), autumn (Tukey’s T=6.3, P<0.01), and winter (Tukey’s T=7.9, P<0.01). Summer species numbers are lower than other seasons because migratory and passage birds have returned to northern nesting areas and can no longer be seen in Hong Kong. Average species richness was highest in spring (41.9), followed by autumn (41.5), winter (39.4), and summer (30.1). In contrast to the golf course proper where 24-52 bird species were recorded in each sampling season, the surrounding non-golf upland shrub habitats on Kau Sai Chau typically supported 4-13 species in 2001 (Ecosystems Ltd., unpubl. data). Similarly, pre-golf bird surveys on Kau Sai Chau recorded 28 species on the northern part of the island over three seasons (September and December 1993 and May 1994) (AXIS Environmental Consultants 1994a, Appendices 2 & 3). Only the two most recent summer counts were lower than the pre-golf cumulative total for 3 seasons. Mean species counts did not differ significantly between years (F = 0.55; P = 0.82). The 2004-5 average species count of 33.5 ranked lowest of the 10 years of sampling (Figure 6.3b). The trendline shown in Figure 6.3b indicates a modest and non-significant decline in mean species numbers. The sharp decline in mean species numbers in 2004-5 is difficult to interpret. It was caused by record low species totals in summer 2004 and winter 2004-5. The summer counts were made on 23-24 July 2004, possibly at a time when some species had begun post-breeding moults. During moult some birds are more secretive because their ability to fly (escape predators) is reduced by the change in plumage. This could have caused some species to go undetected. If we assume that “expected” summer species include those seen during 5 or more summers over the preceding 9 years, we have 7 such species that were not recorded in the tenth summer in 2005: • Little Egret • Cattle Egret • Reef Egret • Yellow Bittern • Night Heron • Common Kingfisher • Long-tailed Tailorbird

Of these, Little Egret, Cattle Egret, Common Kingfisher and Long-tailed Tailorbird are common residents on Kau Sai Chau that were simply not seen or heard during summer 2004. The remaining 3 species (Reef Egret, Yellow Bittern, Night Heron) all appear to have

Ecosystems Ltd. 23 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

declined in abundance on the island. The habitat of Reef Egret is the shoreline and shallow bays, which are sampled only at sites T24, T4, and P13. Reef Egret was most often seen at P13, the point-count site below the dam. Reef Egret is thought to be declining in Hong Kong because of “persecution by fish farmers” (Viney et al. 1996). Yellow Bittern is a summer visitor and passage migrant that nests in mangroves. It was most frequently seen in the marsh at North 15. These were probably passage migrants because there was never evidence of a pair of birds attempting to breed or nest. Night Heron was common in the marsh at North 15 where a roost was formerly located. Night Herons probably continue to feed on Kau Sai Chau, but are not as common on the island after the roost was abandoned. From the above we can conclude that four or five species were probably on the island but not encountered in summer 2004. This would raise the species total near the long-term average of 30 species. A similar analysis for the record low winter 2004-5 count shows a list of 6 species that were recorded 5 or more times over the preceding 9 years: • Little Grebe • Kestrel • Little Ringed Plover • White-breasted Kingfisher • Long-tailed Tailorbird • Yellow-browed Warbler

Of these, 3 species are residents, 2 of which were probably on the island but not encountered: White-breasted Kingfisher and Long-tailed Tailorbird. Little Grebe formerly nested on the island in ponds on the golf course. However, its nesting requirement for standing fresh water with a mixture of open water and vegetation is no longer available in the ponds at Kau Sai Chau. Each of the three migrants (Kestrel, Little Ringed Plover, and Yellow-browed Warbler) can be encountered on most winter days at Kau Sai Chau. Their absence in winter 2004-5 was coincidental. From the above we can conclude that 3-5 “expected” species could have been added to the 2004-5 winter total, yielding a count closer to the long-term average. It is also possible that regional factors affected the numbers of bird species recorded in winter and spring 2004-5. Birds worldwide are known to be under threat and this is true for birds in the East Asian Australasian Flyway (Butchart et al. 2004).

Figure 6.3a Kau Sai Chau mean bird species counts by season from summer 1995 through spring 2005

45

40

35

30

25

20

15 Number of species

10

5

0 Summer Autumn Winter Spring

Ecosystems Ltd. 24 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.3b Kau Sai Chau mean bird species count by year from 1995 through 2004

y = -0.0864x + 38.7 R2 = 0.0101 44 42 40 38 36

each year) 34 32 Mean species count 30 (averaged over 4 seasons 12345678910 Year from opening of golf play

6.3.2 Bird Numbers Total bird counts over 40 sampling seasons spanning 10 years are shown in Figure 6.4. The overall trend has been slightly positive, with an inexplicable 4-year cycle peaking in years 2, 6 and 10. The 2004-5 mean count was the second highest on record. Total counts did not differ significantly between years (F=0.58; P=0.78), due in part to the relatively wide variation between annual counts.

Figure 6.4 Means of four seasonal bird counts per year at Kau Sai Chau 1995-2005

y = 1.1699x + 754.79 1300 R2 = 0.0081 1200 1100 1000 900 800 700 Bird Numbers 600 500 400 Su95 Su96 Su97 Su98 Su99 Su00 Su01 Su02 Su03 Su04

Trends in summer, autumn and winter were positive, but not significantly (Figure 6.5). The slightly positive trend in summer bird counts is encouraging because it suggests the island is supporting greater numbers of nesting birds and their offspring. The slightly positive trend in autumn counts is more difficult to interpret because it may reflect one or more of several changes. There may be increasing numbers of young resident birds fledged on Kau Sai Chau due to the slightly increasing trend in summer bird counts (i.e. more nests) or due to increased survival of young (i.e. more fledglings per nest). Numbers of migrant birds visiting the island might also be increasing due to higher productivity on northern nesting areas or

Ecosystems Ltd. 25 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

enhanced habitat suitability on Kau Sai Chau. The latter explanation is unlikely given the general declining trends in global bird numbers. The spring trend was slightly negative, but not significantly (t = 1.66, P = 0.14). Declining bird counts on spring migration may be due to a number of factors including bird survival on wintering areas further south and habitat suitability on Kau Sai Chau. Counts varied between seasons (F=3.14; P=0.037), with summer having the fewest birds and autumn the most (Figure 6.6). Bird numbers declined from the autumn peak to winter and then further to spring but the mean counts were not significantly different. The lowest average count was for the period 1995-6 (692 birds), and the highest was for the following year (1996-7 total of 879 birds). The average count for the year 2004-5 was 783 birds, second highest over the 10-year sampling period.

Figure 6.5 Total bird counts by season during 40 sampling sessions at Kau Sai Chau from 1995 through 2004

900 850 800 750 700 650 600 550 500 Mean seasonal countbird 450 400 Su Au W Sp

Figure 6.6 Mean bird counts by year at Kau Sai Chau between 1995 and 2005 (n = 10)

y = 6.0288x + 747.12 R2 = 0.0811 900 800 700 600 500 400 300 No. of Birds of No. 200 100 0 12345678910 Year

6.3.3 Dominance Overall dominance of the 40 sample periods since summer 1995 is shown by percentage and species in Table 6.1. 19.5 periods were dominated by Crested Mynah, 12 by Chinese

Ecosystems Ltd. 26 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Bulbuls, 4 by Black-necked Starlings, 1.5 by Black-faced Laughing Thrush, and one each by Richard’s Pipit, Yellow Wagtail and Spotted Munia (Figure 6.7). The four 2004-5 seasons were dominated by Crested Mynah (3) and Chinese Bulbul (1). Average dominance over the 40 sample periods shows that the commonest species typically accounts for 23% of the total count. Although the spring 2004 count was dominated by Crested Mynah (97 birds), a close second was the Black-necked Starling at 131 birds. The greater body weight of the Black-necked Starling means that it was dominant in terms of biomass.

Ecosystems Ltd. 27 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 6.1 Dominant species and percent dominance for all sample sites over all sample periods at Kau Sai Chau between July 1995 and June 2005 Percent Species Total Date Dominant Species Dominan count Count ce Spring 2005 Crested Myna 148 732 20.2 Winter 2004-5 Chinese Bulbul 262 995 26.3 Autumn 2004 Crested Myna 292 853 34.2 Summer 2004 Crested Myna 270 733 36.8 Spring 2004 Crested Myna 97 733 13.2 Winter 2003-4 Chinese Bulbul 87 669 13.0 Autumn 2003 Black-necked Starling 222 980 22.7 Summer 2003 Crested Myna 196 650 30.2 Spring 2003 BFLT* & Crested Myna 62 610 10.2 Winter 2002-3 Chinese Bulbul 205 976 21.0 Autumn 2002 Crested Myna 154 773 19.9 Summer 2002 Crested Myna 200 814 24.6 Spring 2002 Richard's Pipit 75 641 11.7 Winter 2001-2 Chinese Bulbul 161 928 17.3 Autumn 2001 Crested Mynah 196 927 21.1 Summer 2001 Crested Mynah 163 671 24.3 Spring 2001 Black-faced Laughing Thrush 101 727 13.9 Winter 2000-1 Chinese Bulbul 131 743 17.6 Autumn 2000 Crested Mynah 431 1196 36.0 Summer 2000 Crested Mynah 197 690 28.6 Spring 2000 Crested Mynah 86 650 13.2 Winter 1999-00 Black-necked Starling 267 738 36.2 Autumn 1999 Black-necked Starling 120 571 21.0 Summer 1999 Crested Mynah 222 878 25.3 Spring 1999 Yellow Wagtail 204 845 24.1 Winter 1998-9 Chinese Bulbul 162 589 27.5 Autumn 1998 Black-necked Starling 209 873 23.9 Summer 1998 Crested Mynah 113 575 19.7 Spring 1998 Chinese Bulbul 242 767 31.6 Winter 1997-8 Chinese Bulbul 147 680 21.6 Autumn 1997 Crested Mynah 151 872 17.3 Summer 1997 Spotted Munia 176 818 21.5 Spring 1997 Chinese Bulbul 148 673 22.0 Winter 1996-7 Chinese Bulbul 272 1108 24.5 Autumn 1996 Crested Mynah 315 1022 30.8 Summer 1996 Crested Mynah 173 711 24.3 Spring 1996 Chinese Bulbul 186 841 22.1 Winter 1995-6 Chinese Bulbul 237 753 31.5 Autumn 1995 Crested Mynah 74 604 12.3 Summer 1995 Crested Mynah 220 546 40.3 Average dominance 22.7 *BFLT = Black-faced Laughing Thrush

Ecosystems Ltd. 28 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.7 Number of sample seasons during which each of seven species was numerically dominant

20 s 18 16 14 12 10 8 6 4

No. ofSampling Session 2 0 a l h it l a n u g s p i i y lb in u i ta n u rl r P g u M h s a d B ta ' M S T d W d te e g r e s s d n a w t e e e i h o t r in k h c ll o C h c g i e p C e u R Y S -n a k L c d a e l c B a -f k c la B

Mean annual dominance has declined over the first 9 years of sampling from a high of over 26% to a low of 19%. (Figure 6.8). Declining dominance indicates that the most common bird species are accounting for smaller proportions of the bird community on the island. From an ecological perspective this is a positive outcome because it means the bird community is more biodiverse. This is possibly a response to increased habitat quality that has resulted from vegetation recovery following fire control. In the tenth year of sampling dominance increased to an average of 29%. This was due to the large numbers of Crested Mynas in all seasons except winter. This could be a response to the nest box project (see below), which in 2003-2005 provided nest sites for Crested Mynas. Prior to the 2004 nesting season the nest boxes were modified by reducing the diameter of the entrance hole. However, this did not deter Crested Myna nesting because the birds simply pecked at the holes until the diameter was large enough to enter. The nest boxes will be modified again after the end of the 2005 nesting season to reduce the entrance diameter such that Crested Mynas will not be able to enter the boxes.

Ecosystems Ltd. 29 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Figure 6.8 Mean annual dominance of the bird community from 1995-2003

30%

28%

26%

24%

22%

20% Mean percent dominance percent Mean 18%

16% 95-6 96-7 97-8 98-9 99-0 00-1 01-2 02-3 03-4 04-05 Year

6.3.4 Bird Species List The updated list of all bird species recorded on Kau Sai Chau through June 2005 is shown in Table 6.2. To date 135 species representing 34 families of birds have been recorded. Of those, 120 species were recorded during systematic sampling for construction and operation monitoring, of which 2 were added between July 2004 and June 2005. The remaining 15 species were recorded incidental to other work on the island. The species count of 135 represents 30% of the 450 bird species recorded in Hong Kong in the last 50 years on less than 1% of the total land area of Hong Kong SAR. One species, Black-faced Spoonbill, is listed as Endangered in the IUCN Redlist of Threatened Species. This is a common winter resident in Hong Kong, but a vagrant at Kau Sai Chau. It was seen on only one occasion. One species, Peregrine Falcon, is listed in Appendix I of CITES (international trade is prohibited). Eight species are listed in Appendix II of CITES (international trade allowed only with permit). Fourteen species are listed in mainland China as State Class 2 protected species. All wild bird species in Hong Kong SAR are protected under the Wild Animals Protection Ordinance.

6.3.5 Incidental Observations Collared Scops Owl (Otus lempiji) In addition to the Collared Scops Owl that nested in 2004 and 2005 in a nest box, another small owl occasionally roosts at one of the bungalows on the golf course. Regurgitated owl pellets are frequently found beneath the perch. Some 20 pellets were collected for analysis of contents. Preliminary indications are that insects are the dominant component of the owl’s diet. A camera trap was installed in May 2005 in an effort to photograph the owl for species identification. A Crested Myna and a Chinese Starling were photographed, but the owl was not photographed.

6.4 Conclusions 1. The total of 135 species of birds recorded over the 10-year sampling period is encouraging because it represents 30 percent of the total number of species recorded in Hong Kong since the mid-1940s. 2. The continued increase in the total number of species indicates that habitat conditions continue to improve on the island due to protection from hillfire and maturation trees and shrubs in previously fire-damaged habitats.

Ecosystems Ltd. 30 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

3. The number of species recorded during any season exceeds the pre-golf total of 20 species recorded during the four months September-December 1993. 4. The number of bird species recorded in any season on the golf courses exceeds that for non- golf upland shrub habitats on eastern Kau Sai Chau. 5. The year 2004-5 ranked second in average bird abundance but last in average number of species recorded over the 10 years of monitoring. 6. Bird abundance shows a slightly increasing trend for the 10 years of sampling while species numbers show a slightly decreasing trend. 7. Dominance reversed its 9-year downward trend due to increasing numbers of Crested Mynas. This occurred after the 3rd year of the nest box project. The species most often nesting in the nest boxes is Crested Myna. Thus the next boxes must be modified again in 2005 to prevent further nesting of Crested Mynas. 8. Occupancy of a nest box by Collared Scops Owl demonstrates that breeding of owls on Kau Sai Chau may be restricted by availability of suitable nest sites. This suggests that expansion of the nest box project could benefit small owl conservation.

6.5 Recommendations 1. Nest box entrance diameters should be reduced to 3 cm diameter to prevent further occupancy by Crested Mynas. This should be carried out after the 2005 nesting season. 2. One new nest box design, “chimney”, is recommended. The “chimney” is a cylindrical nest box with the opening at the top, which can be fixed under or over branches. This design is not dependent on the availability of large trees. Drainage holes are opened at the base of boxes to drain rainwater. Chimney is designed for Great Tits Parus major, robins and smaller owls (Feu 1989). 3. Additional owl nest boxes should be installed in dense stands of trees where Crested Mynas are unlikely to nest. 4. A shift in monitoring focus will be considered to (i) survey more of the South Course and (ii) simultaneously survey undisturbed shrublands south of the golf course on Kau Sai Chau.

TABLE 6.2 Bird species list for Kau Sai Chau showing local residence and breeding status; degree of global threat; listing under CITES; and protection status in China. Horizontal lines separate taxonomic families Residenc CITES COMMON NAME Species Name Breeding IUCN1 China3 e 2 Status Status 1 Little Grebe Tachybaptus ruficollis R y Phalacrocorax carbo 2 Great Cormorant WV --- sinensis 3 Grey Heron Ardea cinerea R n 4 Purple Heron Ardea purpurea R/PM n 5 Chinese Pond Heron Ardeola bacchus R n 6 Cattle Egret Bubulcus ibis R n 7 Little Green Heron Butoroides striatus R p 8 Great Egret Casmerodius albus R n 9 Little Egret Egretta garzetta R n 10 Intermediate Egret Egretta intermedia R n II 11 Reef Egret Egretta sacra R p II 12 Yellow Bittern Ixobrychus sinensis SV/PM p 13 Night Heron Nycticorax nycticorax R n 14 Black-faced Spoonbill Platalea minor WV --- E II 15 Teal Anas crecca WV --- 16 Crested Goshawk Accipiter trivirgatus R n 2 II 17 Buzzard Buteo buteo WV --- 2 II 18 Black-shouldered Kite Elanus caeruleus PM --- 2 II 19 Bonelli’s Eagle Hieraaetus fasciatus R n 2 II White-bellied Sea 20 Haliaeetus leucogaster R n 2 II Eagle

Ecosystems Ltd. 31 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Residenc CITES COMMON NAME Species Name Breeding IUCN1 China3 e 2 Status Status 21 Black-eared Kite Milvus lineatus R n 2 II 22 Crested Serpent Eagle Spilornis cheela R p 23 Osprey Pandion haliaetus R n 2 II 24 Peregrine Falcon Falco peregrinus R n 1 II 25 Kestrel Falco tinnunculus WV --- 2 II 26 Chinese Francolin Francolinus pintadeanus R y 27 Japanese Quail Coturnix japonica PM/WV --- White-breasted 28 Amaurornis phoenicurus R p Waterhen 29 Moorhen Gallinula chloropus R y 30 Little Ringed Plover Charadrius dubius R y 31 Pacific Golden Plover Pluvialis fulva PM/WV --- 32 Grey-headed Lapwing Vanellus cinereus WV --- 33 Common Sandpiper Actitis hypoleucos PM/WV p 34 Sharp-tailed Sandpiper Calidris acuminata PM --- 35 Sanderling Calidris alba PM --- 36 Red-necked Stint Calidris ruficollis PM/WV --- 37 Long-toed Stint Calidris subminuta PM/WV --- 38 Temminck’s Stint Calidris temminckii PM/WV --- 39 Fantail Snipe Gallinago gallinago PM/WV --- 40 Curlew Numenius arquata PM/WV --- 41 Little Whimbrel Numenius minutus PM --- II 42 Woodcock Scolopax rusticola WV --- 43 Grey-tailed Tattler Tringa brevipes PM --- 44 Wood Sandpiper Tringa glareola PM/WV --- 45 Greenshank Tringa nebularia PM/WV --- 46 Green Sandpiper Tringa ochropus PM/WV --- 47 Marsh Sandpiper Tringa stagnatilis PM/WV --- 48 Redshank Tringa totanus PM/WV --- 49 Black-winged Stilt Himantopus himantopus PM/WV --- 50 Red-necked Phalarope Phalaropus lobatus PM --- 51 Oriental Pratincole Glareola maldivarum NBV --- White-winged Black 52 Chlidonias leucoptera PM --- Tern 53 Emerald Dove Chalcophaps indica R n 54 Pigeon Columba livia R(I) n 55 Spotted Dove Streptopelia chinensis R y 56 Rufous Turtle Dove Streptopelia orientalis PM/WV --- 57 Red Turtle Dove Streptopelia tranquebarica PM/WV --- 58 Plaintive Cuckoo Cacomantis merulinus SV n Chestnut-winged 59 Clamator coromandus SV y Cuckoo 60 Indian Cuckoo Cuculus micropterus SV n 61 Koel Eudynamis scolopacea R p 62 Lesser Coucal Centropus benghalensis R p 63 Greater Coucal Centropus sinensis R y II 64 Collared Scops Owl Otus bakkamoena R y 65 Eagle Owl Bubo bubo R n 66 Savannah Nightjar Caprimulgus affinis R y 67 Common Kingfisher Alcedo atthis R p 68 Pied Kingfisher Ceryle rudis R p Black-capped 69 Halcyon pileata R n Kingfisher White-breasted 70 Halcyon smyrnensis R p Kingfisher

Ecosystems Ltd. 32 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Residenc CITES COMMON NAME Species Name Breeding IUCN1 China3 e 2 Status Status 71 Hoopoe Upupa epops OV n 72 Broad-billed Roller Eurystomus orientalis PM --- 73 Wryneck Jynx torquilla WV --- 74 House Swift Apus nipalensis R/PM n 75 Pacific Swift Apus pacificus R/PM n 76 Barn Swallow Hirundo rustica SV y 77 Red-throated Pipit Anthus cervinus PM/WV --- 78 Olive-backed Pipit Anthus hodgsoni WV --- 79 Richard’s Pipit Anthus richardi R,M,WV p 80 White Wagtail Motacilla alba R p 81 Grey Wagtail Motacilla cinerea PM/WV --- 82 Yellow Wagtail Motacilla flava PM/WV --- 83 Red-vented Bulbul Pycnonotus aurigaster R y 84 Crested Bulbul Pycnonotus jocosus R y 85 Chinese Bulbul Pycnonotus sinensis R y 86 Brown Shrike Lanius cristatus PM/WV --- 87 Rufous-backed Shrike Lanius schach R y Black-browed Reed 88 Acrocephalus bistrigiceps PM --- Warbler 89 Oriental Reed Warbler Acrocephalus orientalis PM --- 90 Chinese Bush Warbler Cettia canturians WV --- 91 Russet Bush Warbler Bradypterus seebohmi WV --- 92 Fantail Warbler Cisticola juncidis R/WV p 93 Magpie Robin Copsychus saularis R y Blue & White 94 Cyanoptila cyanomelana PM --- Flycatcher 95 Siberian Rubythroat Erithacus calliope WV --- 96 Hwamei Garrulax canorus R p Black-faced Laughing- 97 Garrulax perspicillatus R y thrush 98 Blue Rock Thrush Monticola solitarius R n Asian Brown 99 Muscicapa dauurica WV --- Flycatcher Grey-streaked 100 Muscicapa griseisticta WV --- Flycatcher 101 Violet Whistling Thrush Myiophoneus caeruleus R n 102 Common Tailorbird Orthotomus sutorius R y 103 Daurian Redstart Phoenicurus auroreus WV --- 104 Arctic Warbler Phylloscopus borealis PM --- 105 Dusky Warbler Phylloscopus fuscatus WV --- 106 Yellow-browed Warbler Phylloscopus inornatus WV --- 107 Yellow-bellied Prinia Prinia flaviventris R p 108 Plain Prinia Prinia inornata R p 109 Siberian Stonechat Saxicola maura WV --- 110 Red-flanked Bluetail Tarsiger cyanurus WV --- 111 Grey-backed Thrush Turdus hortulorum WV --- 112 Blackbird Turdus merula WV --- 113 Dusky Thrush Turdus naumani WV --- 114 Pale Thrush Turdus pallidus WV --- 115 Japanese White-eye Zosterops japonica R p Yellow-breasted 116 Emberiza aureola PM --- Bunting 117 Yellow-browed Bunting Emberiza chrysophrys PM --- Chestnut-eared 118 Emberiza fucata PM --- Bunting

Ecosystems Ltd. 33 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Residenc CITES COMMON NAME Species Name Breeding IUCN1 China3 e 2 Status Status 119 Little Bunting Emberiza pusilla PM/WV --- 120 Masked Bunting Emberiza spodocephala WV --- 121 Spotted Munia Lonchura punctulata R p 122 White-backed Munia Lonchura striata R p 123 Tree Sparrow Passer montanus R p 124 Crested Mynah Acridotheres cristatellus R p White-cheeked 125 Sturnus cineraceus WV --- Starling 126 Black-necked Starling Sturnus nigricollis R y White-shouldered 127 Sturnus sinensis R n Starling 128 Red-billed Starling Sturnus sericeus WV --- 129 Black-naped Oriole Oriolus chinensis SV --- 130 Black Drongo Dicrurus macrocercus SV y 131 Hair-crested Drongo Dicrurus hottentottus SV n 132 Jungle Crow Corvus macrorhynchus R n 133 Collared Crow Corvus torquatus R n 134 Grey Treepie Dendrocitta formosae R/WV n 135 Magpie Pica pica R y

CITES listing R=resident China protection IUCN listing I = listed in appendix I, WV=winter visitor status E = endangered meaning no international SV=summer visitor 1 = national level-1 trade is permitted I=introduced protected II = listed in appendix II, PM = passage migrant 2 = national level 2 meaning international trade NBV = non-breeding visitor protected is allowed under permit only U = uncertain

Ecosystems Ltd. 34 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

7 MAMMALS

7.1 Bats Monitoring of bats using roost boxes on Kau Sai Chau is discussed under Section 8.2 of this report.

7.2 Predation on Civets by Feral Dogs One Small Indian Civet was found dead on the golf course on 8 May 2005 (Table 7.1). The dead civet was reported by the golf course wardens. 15 civet fatalities have been recorded in the last 7 years, 14 Small Indian Civets and one Masked Palm Civet. All were attributed to attacks by feral dogs. During the 7 years from May 1998 through May 2005 the known loss of civets has averaged over 2 per year. The Masked Palm Civet recovered in 2001 was the only record of this species on Kau Sai Chau.

Table 7.1 List of dead civets recovered on Kau Sai Chau from May 1998 through 30 June 2005 Material Recovered Type Number Small Indian Civet fresh carcass 1 May 1998 Small Indian Civet skeleton 1 May 1998 Small Indian Civet fresh carcass 1 October 1998 Small Indian Civet fresh carcass 1 October 1998 Small Indian Civet fresh carcass 1 May 2001 Masked Palm Civet fresh carcass 1 May 2001 Small Indian Civet fresh carcass 1 3 March 2002 Small Indian Civet fresh carcass 1 6 March 2002 Small Indian Civet fresh carcass 1 27 May 2002 Small Indian Civet fresh carcass 2 July 2002 Small Indian Civet fresh carcass 1 16 October 2002 Small Indian Civet fresh carcass 1 28 July 2003 Small Indian Civet fresh carcass 1 28 November 2003 Small Indian Civet fresh carcass 1 8 May 2005 TOTAL 15

The trapping programme of the greenskeeping staff was successful in removing feral dogs and puppies from the golf course in 2004-5. Box traps provided by the Agriculture, Fisheries & Conservation Department (AFCD) were periodically deployed at various locations on the golf course. Captured dogs were turned over to AFCD for processing. In spite of these control efforts, feral dogs continue to pose a health hazard to humans and a threat to wildlife on Kau Sai Chau. As dogs are removed from the island they are replaced by abandoned dogs or by reproduction among the free-ranging feral population.

7.3 Wild Boar In 2004-5 Wild Boar (Sus scrofa) caused significant damage to turfgrass on the golf course. Boar appeared to be more numerous and more bold as they foraged on and around the golf play areas. Boar were frequently seen by golfers, marshals and greenskeepers during daylight hours. The Hong Kong Police Force (HKPF) and AFCD were asked by KSC to organise Boar hunts but neither agency was able to comply. At the end of fiscal 2004-5 the status of the Boar hunting teams was unknown. We sourced solar-powered electric fence from a manufacturer in Australia. The fence was purchased by KSC. The objective was to experimentally fence golf holes where the

Ecosystems Ltd. 35 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

frequency of damage was highest, then monitor the results for use in planning a long-term strategy for deterring Boar foraging on the golf course. The electric fencing was installed at the periphery of North 5, South 4, and completely surrounding the new North 15 tee from 1 March 2005. After installation of electric fence Boar damage to the fenced areas was stopped. After the initial success with electric fence we recommended shifting the fences to protect other areas where turfgrass was damaged by boar. In May 2005 one fence was re-located from the new North 15 tee to the driving range, where Boar had begun to damage turfgrass in April 2005. To date electric fence has proved a useful tool to deter Wild Boar rooting in turfgrass. One additional and natural agent that might reduce Boar numbers on Kau Sai Chau is Burmese Python Python molurus. There is currently at least one Burmese Python that either visits the island periodically or lives on the island permanently. The snake has been seen many times by the greenskeeping staff. One young Python (±2 m) was recovered from the clubhouse area during June 2005. This suggests that adult Pythons have recently reproduced on the island. Pythons are not poisonous and they have no history of attacking humans. Pythons are constrictors that prey on small to mid-sized mammals and birds. They are known to prey on feral dogs, Barking Deer, Wild Boar and other mammals in Hong Kong. It is hoped that Python presence will be tolerated on KSC in order to build a population of Pythons that would exert predation pressure on feral dogs and young Boar. This could help to reduce the nuisance caused by both. Should the prey base on Kau Sai Chau be inadequate to support released Pythons then surplus snakes would probably swim to nearby islands. Greater numbers of Pythons on KSC represents no known risk or threat to humans. A Wild Boar trapping project was carried out from 10 February through 20 March 2005. A permit for use of corral traps was obtained from AFCD. Dr. Tony James, a doctor of veterinary medicine at Chinese University of Hong Kong, volunteered to euthanise any captured Boar. Two corral traps were assembled with the assistance of personnel at the Golf Workshop. These were installed at North 4 and South 3 and baited with waste fruit and pelleted pig feed. The traps were re-baited and monitored periodically throughout the course of the 6-week project. One prospective trap-site was baited at South 12 but it failed to attract Boar. Another prospective trap-site was baited at North 6 ravine. This site attracted Boar so the trap from South 3 was relocated to North 6. Traps at North 4 and North 6 were set and baited for around 15 days. Boar were seen feeding on bait at both traps and entered the trap on North 4 on several occasions when it was not set for capture. Boar would not enter the traps when set, so a gate was fabricated at the Golf Workshop as an alternate type of entrance. This was deployed for around 10 days without success. On around 18 March Boar stopped foraging on the turfgrass. For the following 7 weeks Boar were seldom seen and there was no damage to turfgrass areas. Because of the poor success of the corral traps we contacted Australian managers who are responsible for controlling feral pig populations. Their trapping methods are similar to those used at Kau Sai Chau with two differences: (i) their corral traps are larger; and (ii) they bait with meat and fermented grains in addition to fruit. Corral traps can be enlarged and meat and/or fermented grain can be sourced for use at Kau Sai Chau. Other trapping options were also pursued. Snares were considered a viable option for several reasons. AFCD indicated that a permit would be issued for the use of snares pending resolution of the issue of euthanising snared Boar.

7.4 Summary Mammals recorded before and after the opening of the golf course are listed in Table 7.2. There were no additional species reported after the Chinese Porcupine was added in 2002.

Ecosystems Ltd. 36 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 7.2 Mammals recorded on Kau Sai Chau from May 1993 through June 2005. Pre-Construction Records - May 1993 to May 1994 Class, Order, Family Common Name Scientific Name Year Recorded Carnivora, Canidae Feral Dog Canis familiaris 1993 Carnivora, Viverridae Small Indian Civet Viverricula indica 1993 Artiodactyla, Suidae Wild Boar Sus scrofa 1996 Rodentia, Muridae Norway Rat Rattus Norvegicus 1994 Post-Construction Records - July 1995 to present Order, Family Common Name Scientific Name Year First Recorded Chiroptera, Rhinolophidae Himalayan Leaf-nosed Hipposideros armiger 2000 Bat Chiroptera, Vespertillionidae Pipistrelle Pipistrellus sp. 2000 Carnivora, Canidae Feral Dog Canis familiaris 1995 Carnivora, Viverridae Small Indian Civet Viverricula indica 1993 Masked Palm Civet Paguma larvata 2001 Artiodactyla, Suidae Wild Boar Sus scrofa 1996 Rodentia, Muridae Norway Rat Rattus norvegicus 1994 Lesser Ricefield Rat Rattus losea 2000 Sikkim Rat Rattus sikkimensis 2000 Rodentia, Hystricidae Chinese Porcupine Hystrix hodgsoni 2002

7.5 Conclusions 1. All four mammals reported before 1994 were recorded on the island during the years 1995- 2005 after golf course construction. Six additional species have been recorded since 1995, two bats, one civet, and three rodents. Of the ten species of mammals on the island, eight are indigenous to Hong Kong and two are introduced (Feral Dog, Norway Rat). 2. Dog trapping by golf course personnel resulted in the removal of many dogs from Kau Sai Chau during 2004-5. However, attacks by feral dogs on civets continued in 2004-5, with one civet killed during the year. This reflects only the one civet that was recovered: other civets may have been killed but never found. While it might be possible for the Small Indian Civet population on Kau Sai Chau to withstand this level of dog predation, the Masked Palm Civet population may not be as large, therefore dog-predation may not be sustainable. Masked Palm Civet was not seen on Kau Sai Chau before or after the single mortality that was attributed to dog attack. 3. Wild Boar did not damage turfgrass that was protected by electric fencing. 4. Electric fencing proved to be a cost-effective and non-destructive means of reducing Wild Boar damage to turfgrass.

7.6 Recommendations 1. Application should be filed with AFCD for a permit to use snares for capture of feral dogs. Snaring would help remove more dogs from the island. 2. Because of continued civet mortalities due to attack by feral dogs, AFCD box traps should be used in conjunction with the snares to capture feral dogs. 3. Electric fences should be moved periodically to areas where boars are damaging unfenced turfgrass. This will enable testing of the effectiveness of electric fencing on many areas of the golf course. One fence was relocated from North 15 tee to the practice range in May 2005. This should be monitored to determine its effectiveness. 4. Burmese Pythons should not be removed from the island. When Pythons are seen near the golf course facilities and removal is chosen as the preferred option, an alternative program is recommended as described below. Burmese python (Python molurus) has occupied Kau Sai Chau at least since construction of the golf course. At least one adult snake is known to occupy Kau Sai Chau for part of the

Ecosystems Ltd. 37 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

year. Little is known of the distribution, movements, or food habits of pythons on Kau Sai Chau. The species is not well understood in Hong Kong and only one short-term radio- telemetric study has been undertaken of its movements. This was on Lantau Island and covered a period of 28 days (Karsen et al. 1998). Pythons are potentially very important to the overall environmental management of the golf course and surrounding habitats for two reasons. First, pythons are carnivorous and, because of their large body size, are potential predators on wild boar and feral dogs. Thus pythons are potentially an effective and organic agent of natural control on populations of feral dogs and wild boar. Second, pythons appear to avoid contact with humans. This explains how pythons live in close association with people yet never attack or otherwise harm them. The proposed study of python movements, habit use, and food habits would be implemented using radio-telemetry and GIS. Radio-transmitters would be surgically implanted in snakes captured on the golf course. This is a standard procedure in the study of snakes and would be done by a veterinary surgeon (probably affiliated with Kadoorie Farm and Botanic Garden, “KFBG”). Pythons would then be released on Kau Sai Chau and subsequently radio-tracked using hand-held equipment. The study would be implemented opportunistically as follows: • pythons would be captured only when the need arose due to their encroachment onto golf course facilities (there would be no pro-active capture effort of free- ranging pythons in the wild); • minimal equipment would be purchased in advance (2-3 transmitters for instrumenting 2-3 snakes, 1-2 receivers, 1-2 antennae, miscellaneous equipment as needed); • advance preparation would be made with veterinary surgeons, who would respond on an as-needed basis; • logistics would be prepared for cooperation with Dr. M. Lau of KFBG for implementation of the study; and • funding agencies would be sought for financial support on an ad-hoc basis.

Objectives of the study would be to describe: • habitat use by pythons (which habitats are used, for what proportion of time); • frequency of use of golf versus non-golf habitats by pythons; • home range size of pythons; • activity budgets of pythons (proportion of time spent resting, foraging-feeding); • prey items of pythons and locations of capture; • frequency of predation by pythons; and • python population numbers on Kau Sai Chau.

Because the study would be implemented only when a python “volunteered” for participation by encroaching on golf facilities, no budget is proposed at this time. A young (<2 m total length) python was captured and removed from Kau Sai Chau in June 2005. This suggests that there may be more young pythons on the island (clutches of eggs can number up to 30). We expect that after a python is captured, anaesthetised, and radio-instrumented it would be sufficiently adverse-conditioned to interaction with humans that upon release it would avoid any further involvement with the golf course and people. For this reason we expect that release of radio-instrumented snakes on the island would not pose a threat to golfers, greenskeepers, visitors or others using the island.

Ecosystems Ltd. 38 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

8 HABITAT MANAGEMENT

8.1 Cormorant Island Cormorant (Phalacrocorax carbo) was first recorded on Kau Sai Chau at the reservoir in winter 2003-2 (see 2002-3 monitoring report). Cormorants are winter visitors to Hong Kong SAR. Their preferred habitats are estuarine and freshwater wetlands in the Northwest New Territories, and marine waters and islands in eastern Hong Kong. Cormorants dive to capture fish, and are effective predators, particularly on pond fish. One reason to attract Cormorants to the Kau Sai Chau reservoir is to increase winter predation on Tilapia (Oreochromis sp.), an introduced and naturalised fish species whose bottom-feeding habit increases turbidity of the reservoir water. Tilapia are prolific breeders and tend to quickly dominate the fish communities in ponds where they are introduced. A typical result is large numbers of stunted Tilapia living in very turbid water. This type of situation is well suited to provision of prey for Cormorants. Cormorant physical adaptations for diving and swimming enable more successful capture of fish, but are not well suited to flight. For example, when Cormorant feathers are exposed to water they quickly become soaked. This helps birds dive and pursue fish with less effort, but is a drawback during flight, when the added weight of the water is a burden. For this reason Cormorants require perches or roosts near water where feathers can be preened and dried. Islands, trees, protruding rocks, man-made structures, and floating debris are all used by Cormorants as drying-roosts. To attract more Cormorants to Kau Sai Chau a floating island to be used as a cormorant roost was constructed and installed in the reservoir on 16 October 2003. Assistance was provided by Sha Tin College students during their Activity Week. The island was made of six wooden shipping pallets joined together by planks and plastic cable-ties, and floated on empty plastic drums. The island was moored in the reservoir, but later broke free of its moorings. It will require improvement of the anchors and addition of camouflage prior to winter 2005-6.

8.2 Bat Roost Boxes Ten roost boxes for bats were installed at Kau Sai Chau in December 2000. The boxes were initially located in habitats as shown in Table 8.1, and were later shifted to locations as shown in Table 8.2. The boxes at the clubhouse were occupied by 1 to 6 Pipistrelles (Pipistrellus sp.) during 2005, similar to occupancy rates during previous years. None of the four boxes at the South 5 maintenance shed was occupied to date. These boxes were moved to the woodland between North 2 and North 8 in spring 2005. Although it was not possible to monitor, we assume that bats continued to roost in the drainage pipes beneath the fairways. The low numbers of bats roosting in boxes at the clubhouse suggests that there may not be a shortage of rousing habitat on the island.

Table 8.1 Locations of 10 bat roost boxes installed at Kau Sai Chau in December 2000 Roost Box No. Location Habitat 1 Clubhouse east Hibiscus trees 2 Clubhouse west Clubhouse wall 3 No. 2 South Green Marsh 4 No. 15 North Tee Marsh woodland 5 No. 15 North Tee Marsh woodland 6 No. 2 North Tee Woodland 7 No. 2 North Tee Woodland 8 No. 2 North Tee Woodland 9 No. 14 South Shed Shed wall 10 No. 14 South Shed Shed wall

Ecosystems Ltd. 39 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Table 8.2 Bat box locations Roost Box No. Location Habitat 1 clubhouse ground floor trees 2 South 5 maintenance shed wall 3 clubhouse ground floor trees 4 clubhouse ground floor trees 5 South 5 maintenance shed wall 6 clubhouse ground floor trees 7 clubhouse ground floor trees 8 clubhouse ground floor trees 9 South 5 maintenance shed wall 10 South 5 maintenance shed wall

8.3 Egretry Planting In early 2000 it was proposed to create an egretry within the golf course area at a site behind the North 11 tee. On 12 April 2000 trees and bamboos were planted with the assistance of greenskeeping personnel and students from Sha Tin College. Selection of tree and bamboo species was based on experience with egretries throughout Hong Kong SAR. Three species of trees were planted (Ficus microcarpa, F. virens, Celtis sinensis) together with one species of bamboo (Bambusa tultoides). Tree survival in 2000-1 was not good, so some dead trees were replaced. By 2003 tree survival had stabilised, but growth rates of trees and bamboos were unacceptably low. It was determined that: (i) maintenance was needed to reduce grass competition for water and nutrients; and (ii) nutrient inputs were needed because of poor soil quality. In 2003-4 grass clippings collected in golf course mowing machines were dumped at the egretry site and then distributed by hand around the bases of trees and bamboos. This was supplemented in 2004-5 by addition of waste plugs/cores that were produced when tees were cored to improve soil conditions. Addition of the mulch and the cores was intended to add organic matter and nutrients to the soil, and thereby enhance tree and bamboo growth and survival. By June 2005 a total of 16 stands of bamboo and 39 of the planted trees survived. Both tree and bamboo growth and vigour had improved greatly (Table 8.3; Appendix 5). Although neither trees nor bamboos are yet large enough to support ardeid nests, growth rates since 2003 have been encouraging. Continued rapid growth of bamboos could enable nesting attempts as early as 2006.

Table 8.3 Average height of tree and bamboo species at egretry planting site Average height Maximum height Total no. Species (m) (to the nearest m) recorded Bambusa tultoides 2.7 5.0 16 Celtis tetrandra subsp. sinensis 2.8 5.5 7 Ficus microcarpa 2.4 4.0 17 Ficus virens subsp. sublanceolata 2.5 4.0 15

8.4 Bird Nest Boxes 8.4.1 Introduction Due to its former use as a firing range, and because of long-term damage by hill-fire prior to 1995, there were virtually no large trees on north Kau Sai Chau before the construction of the golf course. With protection from hillfire tree cover has increased over the last 10 years from both natural seeding and planting. However, most trees are not yet large enough to provide tree holes or cavities for bird nesting. To compensate for the shortage of breeding habitats for owls and other cavity-nesters, we installed nest-boxes at Kau Sai Chau prior to the nesting season in 2003. Anticipated benefits of the project were:

Ecosystems Ltd. 40 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

1. increased numbers of cavity-nesting birds; 2. increased numbers of nesting Collared Scops Owls; 3. increased predation by owls on rodents and snakes; 4. enhanced public relations through demonstrated commitment to nature conservation; and 5. enhanced awareness of nature conservation among golf course personnel and golfers.

8.4.2 Methods & Materials Nest boxes were built according to the design that proved most attractive to Collared Scops Owls in an AFCD project (Lock 2002). Eleven boxes were installed in March and April 2003. The nest box dimensions were 16 x 21 x 44.5 cm, with an entrance hole diameter of 7 cm. Because many boxes were occupied by Crested Mynas in 2003, we reduced the diameter of the entrance hole to 3.5 cm prior to the 2004 nesting season. The top of each box is a hinged door that opens for monitoring. Eleven nest boxes were installed on trees with large, closed canopies. A geographic positioning system (GPS) was used to plot all nest box locations and each box was numbered. The heights of the box entrances above ground were measured. Boxes were monitored twice between April and May. Nesting birds were identified to species and young (near-fledglings) were counted. Numbers of eggs and/or chicks were recorded. Occupied nests were photographed. Prior to the nesting season all boxes were cleaned. All non-target occupants, e.g., ants, bees, wasps, were removed from nest boxes.

8.4.3 Results Birds nested in 9 boxes in 2005, an increase from 7 in 2004 and 5 in 2003 (Table 8.4). Apart from one Collared Scops Owl (Otus lempiji), all were Crested Myna Acridotheres cristatellus nests. Crested Mynas were able to enter the nest boxes in spite of the reduced diameter of the entrance hole. They did this by pecking at the wooden entrance hole until it was large enough to enter.

Table 8.4 Nest box history

Year No. of No. of % No. of Species (no. of nests) Installed Occupied Occupancy Species Boxes Boxes 2003 11 5 45 1 Crested Myna (5 nests) 2004 11 7 64 2 Crested Myna (6 nests) Collared Scops Owl (1 nest) 2005 11 9 82 2 Crested Myna (8 nests) Collared Scops Owl (1 nest)

Crested Myna is a common resident in Hong Kong that is usually found in urban and open areas (e.g., villages, cultivation). It is the most common bird on Kau Sai Chau (see Figure 6.6a). Crested Mynas in South China usually lay eggs in May (Cheng 1993). The nests of Crested Myna are usually built in crevices of buildings, tree holes and abandoned nests of Magpie Pica pica and Black-necked Starling Sturnus nigricollis (ibid.). The brood size recorded in this study (4-6 eggs) was similar to that reported by Cheng (1993): typically 4 eggs per nest with a maximum of 6 eggs. The occupation rate in 2005 was considered high as nesting occurred in all but 2 of the boxes. This showed that nesting habitats may be a limiting factor for bird reproduction on northern Kau Sai Chau. In 2003 only Crested Myna nested. In 2004 Collared Scops Owl nested in a box near the North 2 tee. This was the first visual record of Collared Scops Owl on Kau Sai Chau. The same nest box was occupied again by Collared Scops Owl in 2005 (Table 8.5). Although the nest box was located near a buggy path and therefore subject to noise, the nesting owls disregarded golfers, golf course personnel and maintenance equipment.

Ecosystems Ltd. 41 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Box number 11 was relocated in 2004 because of loss of the nest tree. The box was shifted to the woodland on the right side of North 2 fairway near the active Collared Scops Owl nest. The nest entrance diameter was restored to 7 cm, a size suitable for owls. Box number 4 was relocated from the North 14 green area to the South 3 green kiosk.

Table 8.5 Contents of each nest box in spring 2005 Nest 25 April 18 May 05 Height Tree species Location Notes Box 05 (m) 1 4 eggs Collared 3.5 Schefflera woods at North of Scops Owl on heptaphylla 2 tee Collared nest Scops Owl 2 occupie no birds 3.9 Macaranga ravine North 6 d by present; tanarius right honey honey bees no bees longer present 3 no bird 4 Crested 3.5 Acacia North 10 right activity Myna chicks, confusa 1 egg 4 no bird 5 Crested 3.6 Sapium South 3 green moved from activity Myna eggs sebiferum kiosk North 14 green in 2005 5 no bird 4 chicks, 2 3.1 Cleistocalyx South 2 green activity eggs Crested operculata left Myna 6 no bird 5 eggs 3.7 Cinnamomu South 18 green activity Crested Myna m burmanii right 7 5 eggs 2 chicks 2.9 Macaranga North 14 red Crested Crested Myna tanarius tee Myna 8 no bird 5 chicks 3.1 Macaranga South 15 green activity Crested Myna tanarius 9 no bird no bird activity 3.0 Macaranga turf nursery activity tanarius helipad 10 2 eggs 4 chicks 3.4 Hibiscus clubhouse Crested Crested Myna tiliaceus practice green Myna 11 no bird 1 egg Crested 3.1 Schefflera North 2 right new location in activity Myna heptaphylla woods 2005; H. tiliaceus tree fell in 2004

8.5 Conclusions 1. The Cormorant roost/perch island requires re-construction, addition of camouflage and re- installation in the reservoir. 2. There is an abundant resource of bat prey (flying insects) at Kau Sai Chau, and bats are abundant on the island. The bat roost-box project was implemented on the assumption thatbat numbers were limited by the availability of suitable roost sites. However, bats are now known to roost successfully in the large-diameter drainage pipes beneath the fairways and in the patio umbrellas at the clubhouse. The low rate of roost-box occupancy may be due to the fact that other preferred roost sites are available. This may indicate that the locations or designs of the roost boxes are not well suited to bat occupancy, or that roosting sites are not limiting. Because of this outcome, we recommend discontinuing the roost-box project in 2005-6.

Ecosystems Ltd. 42 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

3. Horticultural measures (mulching and weeding) at the egretry have greatly improved growth rates and vigour of planted trees and bamboos. Mulching with grass clippings and waste materials from coring of tees should be continued through 2005-6. 4. Bird nest boxes have been occupied during all three years they have been installed. Percent occupancy has increased from 45% in 2003 to 82% in 2005. A nesting first occupied by Collared Scops Owls in 2004 was occupied again in 2005. This is the second known nesting attempt of Collared Scops Owl on Kau Sai Chau.

8.6 Potential habitats for Schrenck’s Bittern on Kau Sai Chau Golf Course 8.6.1 Introduction Schrenck’s Bittern Ixobrychus eurhythmus is a rare passage migrant, but formerly breed in Hong Kong (Herklots 1953). According to Carey et al. (2001), the last record of nesting of this species in Hong Kong happened in the 1950’s. Schrenck’s Bittern, though still recorded from widespread locations in Hong Kong (mostly in Luk Keng marsh of Northeast New Territories), is probably extinct as a breeding species in Hong Kong. This may be related to the gradual loss of wetland habitats in the last few decades. A probable sighting of nesting of this species was recorded on Yim Tin Tsai, a small island on the north of Kau Sai Chau, in June 2004 (T.H. Lui, pers. comm.). A Schrenck’s Bittern carrying nesting materials landed on the brackish grassy marsh, which are abandoned saltpans constructed in the nineteenth century. Small breeding populations of Schrenck’s Bittern may still struggle in remote areas in Hong Kong. Kau Sai Chau is near Yim Tin Tsai and has freshwater habitats on the golf course. With appropriate modification, ponds and marshes on the golf course may attract dispersing juveniles or adult Schrenck’s Bitterns. The marsh on Yim Tin Tsai was visited on 22 September 2004 to investigate this possibility.

8.6.2 Methods & Materials Marshes on Yim Tin Tsai was visited on 22 September 2004. Photos of the marshes were taken. Background information of ecology of Schrenck’s Bittern was supplemented by literature reviews.

8.6.3 Results The marsh was wet and brackish, and mainly covered by Interrupted Tri-vein Fern Cyclosorus interruptus 1 m tall (Appendix 6). No sighting of Schrenck’s Bittern was observed. Schrenck’s Bittern usually nests in reedbed, grassy marshes, paddy fields and streambank (Zhu and Zou 2001). The nest is a shallow dish composed of reed and leaves supported by bended reed. Food of juveniles includes small fishes, pawns, frogs and insects (Chu and Qiu 1999, Zhu and Zou 2001). Clutch size is 4-6 eggs (ibid.).

8.6.4 Recommendations The regular records of Yellow Bittern Ixobrychus sinensis, a species of the same genus as Schrenck’s Bittern, in the ponds near the clubhouse demonstrates that there is suitable bittern habitat on Kau Sai Chau. The creation of potential habitats for this species may not need dramatic modification of the existing ponds on the golf course. The marsh at North 15 is an example of suitable bittern habitat (Appendix 6). Similar habitats for Schrenck’s Bittern could be created if this did not conflict with the overall management of the golf course. New ponds to be created for the golf course extension might be suitable sites for habitat creation.

8.6.5 Recommendations 1. Bat roost boxes a. relocate remaining bat roost boxes from the Administration Building to woodlands

Ecosystems Ltd. 43 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

b. discontinue monitoring 2. Egretry plantation a. continue periodic weeding around trees b. continue mulching with grass clippings c. continue mulching with cores from tees and/or greens 3. Bird nest boxes a. reduce nest entrance diameters to 3 cm to enable nesting by Magpie Robin, Great Tit and other small birds b. install smaller nest boxes near the clubhouse to attract Magpie Robin and Great Tit 4. Enhancement of water bodies a. select a number of species of native aquatic vegetatation for introduction around the perimeter of the golf course ponds. b. plant or introduce these species and monitor survival

Ecosystems Ltd. 44 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

9 CONSERVATION EDUCATION

9.1 Nature Gallery Two Nature Gallery exhibits entitled ”Exotic Species” and “About Butterflies” were prepared and displayed during 2004-5 (Appendix 7). The purpose of the display is to provide information to golfers and staff of the golf course about wildlife occurred on the island, and also provide safety guidelines when a wild animal is encountered.

9.2 Bird of the Month The bird of the month display continued in 2004-5 with White-bellied Sea Eagle Haliaeetus leucogaster, Oriental Pratincole Glareola maldivarum, Common Buzzard Buteo buteo and Magpie Robin Copsychus saularis.

9.3 Field Trip & Seminar We coordinated with the Golf Course to organize a day field trip for Shatin College students on 15 October 2004. Activities included a visit to the mangrove planting area, Wild Boar trap, bird box checking and slide shows (Appendices 8a-8c). A seminar “Birds of Kau Sai Chau Golf Course” was given to field workers of the golf course on 1 April 2005.

Ecosystems Ltd. 45 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

10 REFERENCES Ades, G. 1999. The species composition, distribution and population size of Hong Kong bats. Memoirs of Hong Kong Natural. History Society 22:183-209. AXIS Environmental Consultants Ltd. 1994. Kau Sai Chau Development Additional Ecological Survey. The Jockey Club Kau Sai Chau Public Golf Course Limited, Hong Kong. Berger, W.H. and F.L. Parker. 1970. Diversity of planktonic Foraminifera in deep sea sediments. Science 168:1345-7. Burnham, K.P., D.R. Anderson and J.L. Laake. 1980. Estimation of density from line transect sampling of biological populations. Wildlife Monographs 72:1-200. Butchart, S. H. M, Stattersfield A. J, Bennun L. A., Shutes, S. M., Akçakaya H.R. 2004. Measuring Global Trends in the Status of Biodiversity: Red List Indices for Birds. PLoS Biol 2(12): e383 Carey, G.J., Chalmers, M.L., Diskin, D.A., Kennerley, P.R., Leader, P.J., Leven, M.R., Lewthwaite, R.W., Melville, D.S., Turnbull, M. and Young, L. 2001. The Avifauna of Hong Kong. Hong Kong Bird Watching Society, Hong Kong. Cheng, T.H. 1993. Economic Birds of China. Science Press, Beijing. Chu, Z.Y. and Qiu, Z.Z. 1999. Breeding ecology of Schrenck’s Bittern. Chinese Wildlife 4: 8- 9. Dudgeon, D. and Corlett, R. 1994. Hills and Streams - An Ecology of Hong Kong. Hong Kong University Press, Hong Kong. Feu, C.D. 1989. Nestboxes: BTO Guide 20. The British Trust for Ornithology, Hertfordshire. Herklots, G.A.C. 1953. Hong Kong Birds. South China Morning Post, Hong Kong. Hyder. 1997. Kau Sai Chau Golf Centre Operational Phase Environmental Monitoring and Audit Report: February 1st – April 30th 1997. The Jockey Club Kau Sai Chau Public Golf Course Limited, Hong Kong. Karsen, S. J., M.W. Lau, and A. Bogadek. 1986. Hong Kong Amphibians and Reptiles. Urban Council, Hong Kong, 136pp. Lau, M.W.N. and D. Dudgeon. 1999. Composition and distribution of Hong Kong Amphibian fauna. Memoirs of the Hong Kong Natural History Society 22: 1-80. Magurran, A. E. 1988. Ecological Diversity and Its Measurement. Croom Helm Ltd., London, 179pp. Preston-Mafham, R. and K, Preston-Mafham. 1988. Butterflies of the World. Blendford Press, London. Reynolds, R.Y., J.M. Scott and R.A. Nussbaum. 1980. A variable circular plot method for estimating bird numbers. Condor 82:309-313. Viney, C., K. Phillipps, and C.Y. Lam. 1994. Birds of Hong Kong and South China. Government Printer, Hong Kong. Wang, S., 1998. China red data book of endangered animals: Pisces. Science Press, Beijing. Wilson, K.D.P. 1995. Hong Kong Dragonflies. Urban Council, Hong Kong. Young, J.J. and Reels, G.T. 1998. A brief note on the distribution and conservation of Birdwing butterflies in Hong Kong. Porcupine! 17: 10-11. Zar, J. H. 1984. Biostatistical Analysis. Prentice-Hall, Inc. Englewood Cliffs, New Jersey. Zhao, E. 1998. China Red Data Book of Endangered Animals. Amphibia & Reptilia. Science Press, Beijing. Zhu, X. and Zou, X.P. 2001. The Herons of China. China Forestry Publishing House, Beijing.

Ecosystems Ltd. 46 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 1. Ecological Monitoring Schedule at Kau Sai Chau Golf Course, July 2004 to June 2005.

2004 2005 Task Jul Aug Sep Oct Nov Dec Jan Feb Mar Apr May Jun July Mangrove monitoring Invertebrate monitoring Amphibian monitoring Bird monitoring Nest box monitoring Bat box monitoring Wild Boar trapping

Ecosystems Ltd. 48 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 2a. Mangrove planting site below the dam

Ecosystems Ltd. 49 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 2b. Mangrove planting layout at Site E

Ecosystems Ltd. 50 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 3 Marbled Eel Anguilla marmorota captured in the pond east of North 2 green in spring 2005.

Appendix 4 Chinese Cobra Naja atra

Ecosystems Ltd. 51 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 5 Egretry tree planting site

Appendix 6 Marshes on Yim Tin Tsai (left) & near workshop (right)

Ecosystems Ltd. 52 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 7 Nature Gallery display at clubhouse for conservation education

Ecosystems Ltd. 53 Hong Kong Jockey Club Kau Sai Chau Public Golf Course Ltd Ecological Monitoring Report July 2004 to June 2005

Appendix 8a Visit to Wild Boar trap

Appendix 8b Bird box checking

Appendix 8c Slide show

Ecosystems Ltd. 54