A REVIEW OF THE ADVERSE EFFECTS OF CASUARINA SPP. ON COASTAL ECOSYSTEMS AND SEA TURTLE NESTING BEACHES

DIPA AWALE & ANDREA D PHILLOTT

Asian University for Women, Chittagong, Bangladesh

andrea.phillott@auw.edu.bd

Download article as PDF

Introduction

Casuarina spp. are extensively cultivated worldwide for beach establishment, erosion control, wind breaking, coastal sand dune stabilization, and as ornamental trees (NRC, 1984). Throughout Asia, bioshields of Casuarina spp. are also recommended for construction (Danielsen et al., 2005; Kesavan & Swaminathan, 2006; De Zoysa, 2008; Mattsson et al., 2009) or reinforcement (Tanaka, 2009; Samarakoon et al., 2013) to mitigate the impacts of future tsunamis and other natural disasters.

However, Casuarina spp. reduce biological diversity and beach integrity, and C. equisetifolia has been reported as a serious invasive species in many coastal regions of the world, including Florida and Hawaii in the USA, countries throughout the Caribbean Sea (Wheeler et al., 2011), and the Republic of Palau in the Pacific Ocean (Space et al., 2003). Eight of 33 countries at the 2012 IOSEA Marine Turtle Memorandum of Understanding meeting described the planting of Casuarina spp. as a current conservation activity, yet six countries identified it as a problem on their nesting beaches (see http://iosea-reporting.org/test/reporting/Test.asp).

Natural growth of Casuarina spp. and effect on beach ecosystems

The Genus Casuarina, of the Family Casuarinaceae, contains 17 species. Casuarina equisetifolia, commonly known as the beach she-oak, beef wood, or Australian pine, has the widest distribution of all Casuarina species and is native from Australia eastward to Melanesia and westward to coastal Southeast Asia (Whistler & Elevitch, 2006). Casuarina spp. are capable of very fast growth, require little attention, and thrive in sandy and saline conditions. The natural habitat is semi-arid to sub-humid, with a mean annual temperature of 10-35°C and mean annual rainfall of 200-3,500mm. Casuarina spp. grow best in well-drained and coarse-textured soils, such as sands and sandy loams, occur naturally on sand dunes, in sands alongside estuaries and behind fore-dunes, and on gentle slopes near the sea, and persist at the leading edge of dune vegetation where plants are subject to salt spray and inundation with seawater at extremely high tides (Hanum & van der Maesen, 1997).

Although very little is known about the effects of salinity on its physiology and biochemistry, basic metabolic adaptations such as the accumulation of osmolytes (e.g. proline), as occurs in other saline-tolerant plants, may ensure adaptability to the saline stress (Desingh, 2002; Tani & Sasakawa, 2006). The accumulation of antioxidant enzymes may also contribute to the tolerance of Casuarina spp. to salinity (Desingh, 2002). Tolerance to adverse environmental conditions allows Casuarina spp. to easily colonise new environments, after which it can often outcompete other species due to its mode of reproduction. Casuarina spp. are both monoecious and dioecious; the genera reproduces sexually, via seed, and vegetatively through the sprouting of new clonal trunks from existing rootstock (Hanum & van der Maesen, 1997) or by rooting along branches that touch the ground (Whistler & Elevitch, 2006). Some Casuarina spp. are capable of flowering year long, so individual trees can produce thousands of seeds in a year, with each seed remaining viable for up to a year and germinating within 4-8 days under suitable conditions (Hanum & van der Maesen, 1997). Wind pollination aids in rapid seed dispersal over a large area (Whistler & Elevitch, 2006). These characteristics contribute to the production of a large number of seedlings in a short period of time.

Stands of Casuarina spp. compete easily with native vegetation, as actinorhizal root nodules that form with a bacterial symbiont of the genus Frankia allow the trees to fix nitrogen (Potgieter et al., 2014). Once established, they displace native vegetation by producing heavy shade and a thick layer of leaf litter; the genera can accumulate up to 120 t/ha of litter (Bernhard-Reversat & Loumeto, 2002). Such thick accumulation of leaf litter, and the production of phytotoxic allelopathic compounds, inhibits the germination and seedling growth of understorey vegetation (Batish & Singh, 1998; Batish et al., 2001). Thus, these species can form monocultures and alter soil chemistry to further inhibit competitors (Batish et al., 2001).

The high primary production of Casuarina spp. may be aided by strategies that reduce the decomposition rate of leaf litter and improving the synchrony between mineralization and uptake. Although leaf decomposition rate is affected by both litter type and the forest type of invaded sites (Hata et al., 2012), the tannin concentration of Casuarina spp. leaves inhibit decomposition of litter and soil organic matter, form tannin-protein complexes relatively resistant to decomposition, induce toxicity to microbial populations, and inhibit microbial enzyme activities (Zhang et al., 2013). The ecological consequences of elevated tannin levels may include allelopathic responses, changes in soil quality and reduced ecosystem productivity. These effects may also alter or control succession pathways of natural vegetation (Kraus et al., 2003) and, therefore, beach structure.

Impacts of Casuarina spp. on beach structure

Beaches are not rigid or permanent structures; they are maintained by seasonal weather and wave action. Coastal dunes are formed by the aeolian (wind) transport of sand from the near-shore to the back-beach. The first plant colonisers of the bare sand, usually grasses or small shrubs (Martinez et al., 2001), reduce wind velocity and the capacity for aeolian transport and trap sand (reviewed by Sloss et al., 2012). Growth of the pioneer species is stimulated by sand entrapment and accumulation, and the roots begin to bind the surface sand layers together. As the substrate becomes more stable and suitable for successive plant species to colonise, humus formed from the decomposition of fallen vegetation increases substrate nutrition, cohesion, and water retention (reviewed by Pye, 1982; Martinez et al., 2001) and promotes further growth.

Abundant native vegetation on the dunes traps sand and aids in progressive widening of the beach; an annual addition of up to 10,000 cubic meters of sand per kilometer of beach is possible on a well vegetated dune (see Sealey, 2006). Introduced Casuarina spp. out- competes or inhibits native vegetation and destabilizes the beach as sand is deposited between the Casuarina trees instead of accumulating vertically in front of dune- stabilising grasses. The beach subsequently becomes flattened and can be more easily stripped of sand by waves during severe storms to create a steep beach, which further erodes to become a narrow beach (see Gordon, 1998; Burroughs & Tebbens, 2008; Schmid et al., 2008). With each successive storm, the beach shrinks to the Casuarina tree line (Schmid et al., 2008). Beach destruction may eventually occur if the erosion continues and there is insufficient sand in the longshore currents to rebuild the beach by normal processes (Samsuddin & Suchindan, 1987). Casuarina trees are also prone to falling because of their height and shallow root system (Sealey, 2006; Schmid et al., 2008) so erosion continues as the front trees are uprooted and washed away (Sealey, 2006).

19-06-01

Impacts of Casuarina spp. on sea turtles and their nests

Casuarina spp. are often planted on sea turtle nesting beaches (Figure 1) as a physical shield between urban areas and the ocean so as to reduce light levels and create suitable photic conditions for nesting (Salmon et al., 1995) or as shade during adaptive practices to manage the effect of rising ambient temperatures resulting from global climate change on sea turtle nests (Wood et al., 2014). However, if Casuarina spp. are allowed to alter beach structure, nesting and hatching success may be reduced and natural hatchling sex ratios altered.

Stands of Casuarina spp. are only likely to be a moderate impediment to nesting sea turtles that can maneuver around them to nest (Witherington et al., 2011), but fallen trees can create physical obstacles for nesting females to navigate (NRC, 1984) and result in abandoned nesting attempts or nesting in sub-optimal areas. The dense, shallow roots of Casuarina spp. may interfere with nest construction so females abandon their nesting attempts (NRC, 1984; Wood et al., 2014) or penetrate the nest and destroy eggs during incubation (Hays and Speakman, 1993; Leslie et al., 1996). Hatchlings emerging from nests laid within dense forests are at risk of entanglement in roots during emergence or disorientation into supralittoral vegetation (Godfrey and Baretto, 1995).

The formation of significantly steeper and narrower beaches in the presence of dense stands of Casuarina spp. may impact hatchling survival as nests laid close to the sea are at risk of egg loss due to erosion and mortality due to salt water inundation (Foley et al., 2006; Caut et al., 2010). Nest temperatures during incubation may be lowered by Casuarina spp. shading nests (Morreale et al., 1982; Spotila et al.,1987; Kamel, 2013), lowering the water table and exhausting soil moisture (NRC, 1984), or blanketing the beach surface with a thick layer of leaf litter (NBII & ISSG, 2010). Lower nest temperatures can skew hatchling sex ratios to result in more males and reduce hatchling swimming performance (e.g. Burgess et al., 2006). The relationship between the primary sex ratios of hatchlings, hatchling fitness, and the operating sex ratios of adult populations is currently unknown, but the resulting population demographics may influence the capacity of a species to persist during global climate change (Stewart & Dutton, 2014).

Recommendations

Beach vegetation initiatives should be carefully planned to ensure dune preservation and stability (see comments by Mascarenhas, 2006) and utilise indigenous plant species instead of exotics or invasives such as Casuarina spp. Natural forests in relatively undisturbed areas can be examined to determine the species most likely to grow in different localities, and can possibly be sourced from local NGOs or communities. If little natural forest remains, then local botanists may be able to suggest the most suitable species. The removal of existing stands of Casuarina trees can be expensive and time consuming, but a priority in areas where nesting and hatching success is low. Careful, physical removal is likely to have less effect on the environment, and sea turtle nests, than methods of chemical or biological control (see Conrad et al., 2011; Wheeler et al., 2011).

The problems experienced on beaches planted with Casuarina spp. should be remembered when plans to introduce exotic species or interfere with natural beach processes are considered. Other methods of stabilization, including groin construction, beach dewatering, beach nourishment (Grain et al., 1995), piling installation (Bouchard et al., 1998), and artificial reef construction also change beach dynamics and have an adverse impact on sea turtles; it should be remembered that beaches are dynamic structures and local development should be prepared to cope with a changing environment.

Literature cited

Batish, D.R. & H.P. Singh. 1998. Role of allelopathy in regulating the understorey vegetation of Casuarina equisetifolia. Environmental Forest Science 54: 317-323.

Batish, D.R., H.P. Singh & R.K. Kohli. 2001. Vegetation exclusion under Casuarina equisetifolia L.: Does allelopathy play a role? Community Ecology 2:93-100.

Bernhard-Reversat, F. & J. J. Loumeto. 2002. ‘The litter system in African forest-tree plantations’, in V. M. Reddy (ed.), Management of Tropical Plantation-forests and Their Soil-litter System, Science Publishers Inc., Enfield, New Hampshire, U.S.A., pp. 11-39.

Burgess, E., D.T. Booth & J.M. Lanyon. 2006. Swimming performance of hatchling green turtles is affected by incubation temperature. Coral Reefs 25: 341-349.

Bouchard, S., K. Moran, M. Tiwari, D. Wood, A. Bolten, P. Eliazar & K. Bjorndal. 1998. Effects of exposed pilings on sea turtle nesting activity at Melbourne Beach, Florida. Journal of Coastal Research 14: 1343-1347.

Burroughs, S.M. & S.F. Tebbens. 2008. Dune retreat and shoreline change on the outer banks of North Carolina. Journal of Coastal Research 24: 104-112.

Caut. S., E. Guirlet & M. Girondot. 2010. Effect of tidal wash on the embryonic development of leatherback turtles in French Guiana. Marine Environmental Research 69: 254- 261.

Conrad, J.R., J. Wyneken, J.A. Garner & S. Garner. 2011. Experimental study of dune vegetation impact and control on leatherback sea turtle Dermochelys coriacea nests. Endangered Species Research 15: 13-27.

Danielsen, F., M.K. Sorensen, M.F. Olwig, V. Selvam, F. Parish, N.D. Burgess & T. Hiraishi et al. 2005. The Asian tsunami: A protective role for coastal vegetation. Science 310: 643.

January 2014

17

Indian Ocean Turtle Newsletter No. 19

18

Desingh, R. 2002. Variation in Salinity Stress Tolerance Among Three Casuarina Species. PhD Thesis. Pondicherry University, Pondicherry, India.

De Zoysa, M. 2008. Casuarina coastal forest shelterbelts in Hambantota City, Sri Lanka: Assessment of impacts. Small- Scale Forestry 7: 17-27.

Foley, A.M., S.A. Peck & G.R. Harman. 2006. Effects of sand characteristics and inundation on the hatching success of loggerhead sea turtle (Caretta caretta) clutches on low- relief mangrove islands in southwest Florida. Chelonian Conservation and Biology 5: 32-41.

Godfrey, M.H. & R. Barreto. 1995. Beach vegetation and sea finding orientation of turtle hatchlings. Biological Conservation 74: 29-32.

Gordon, D.R. 1998. Effects of invasive non-indigenous plant species on ecosystem processed: Lessons from Florida. Ecological Concepts in Conservation Biology 8: 975-989.

Grain, D.A., A.B. Bolten & K.A. Bjorndal. 1995. Effects of beach nourishment on sea turtles: Review and research initiatives. Restoration Ecology 3: 95-104.

Hanum, F. & L.J.G. van der Maesen. 1997. Plant Resources of South-East Asia 11. Auxiliary Plants. PROSEA Foundation, Bogor, Indonesia.

Hata, K., H. Kato, & N. Kachi. 2012. Leaf litter of the invasive Casuarina equisetifolia decomposes at the same rate as that of native woody species on oceanic islands but releases more nitrogen. Weed Research 52:542-550.

Hays, G.C. & J.R. Speakman. 1993. Nest placement by loggerhead turtles. Animal Behavior 45: 47-53.

Kamel, S.J. 2013. Vegetation cover predicts temperatures in nests of the hawksbill sea turtle: Implications for beach management and offspring sex ratio. Endangered Species Research 20: 41-38.

Kesavan, P.C. & M.S. Swaminathan. 2006. Managing extreme natural disasters in coastal areas. Philosophical Transactions: Mathematical, Physical and Engineering Sciences 364: 2191-2216.

Kraus, T.E.C., R.A. Dahlgren, & R.J. Zasoski. 2003. Tannins in nutrient dynamics of forest ecosystems-A review. Plant and Soil 256: 41-66.

Leslie, A.J., D.N. Penick, J.R. Spotila & F.V. Paladino. 1996. Leatherback turtle, Dermochelys coriacea, nesting and nest

success at Tortuguero, Costa Rica, in 1990-1991. Chelonian Conservation and Biology 2:159-168.

Martínez, M.L., G. Vázquez & S. Sánchez Colón. 2001. Spatial and temporal variability during primary succession on tropical coastal sand dunes. Journal of Vegetation Science 12: 361-372.

Mascarenhas, A. 2006. Extreme events, intrinsic landforms and humankind: post-tsunami scenario along Nagore– Velankanni coast, Tamil Nadu, India. Current Science 90: 1195-1201.

Mattsson, E., M. Ostwald, S.P. Nissanka, B. Holmer & M. Palm. 2009. Recovery and protection of coastal ecosystems after tsunami event and potential for participatory forestry CDM – Examples from Sri Lanka. Ocean and Costal Management 52: 1-9.

Morreale, S.J., G.J. Ruiz, J.R. Spotila & E.A. Standora. 1982. Temperature-dependent sex determination: Current practices threaten conservation of sea turtles. Science 216: 1245-1247.

NBII & ISSG (National Biological Information Infrastructures & IUCN/SSC Invasive Species Special Group). 2010. Casurina equisetifolia (tree). Global Invasive Species. Retrieved from http://www.issg.org/database/ species/ecology.asp?fr=1&si=365 on December 16, 2012.

NRC (National Research Council). 1984. Casuarinas: Nitrogen-Fixing Trees for Adverse Sites. National Academy Press, Washington D.C., USA.

Potgieter, L.J., D.M. Richardson & J.R.U. Wilson. 2014. Casuarina: Biogeography and ecology of an important tree genus in a changing world. Biological Invasions 16: 609-633.

Pye, K. 1982. Morphological development of coastal dunes in a humid tropical environment, Cape Bedford and Cape Flattery, North Queensland. Geografiska Annaler 64A: 213- 227.

Salmon, M., R. Reiners, C. Lavin & J. Wyneken. 1995. Behavior of loggerhead sea turtles on an urban beach. I. Correlates of nest placement. Journal of Herpetology 29: 560- 567.

Samarakoon, M.B., N. Tanaka & K. Limura. 2013. Improvement of effectiveness of existing Casuarina equisetifolia forests in mitigating tsunami damage. Journal of Environmental Management 15: 105-114.

Samsuddin, M. & G.K. Suchindan. 1987. Beach erosion and

accretion in relation to seasonal longshore current variation in the northern Kerala coast, India. Journal of Coastal Research 3: 55-62.

Schmid, J. L., D. S. Addison, M.A. Donnelly, M.A. Shirley & T. Wibbels. 2008. The effect of Australian pine (Casuarina equisetifolia) removal on loggerhead sea turtle (Caretta caretta) incubation temperatures on Keewaydin Island, Florida. Journal of Coastal Research 55: 214-220.

Sealey, N. 2006. The cycle of Casurina-induced beach erosion-A case study from Andros, Bahamas. In: Davis R.L. ad Gamble D.W. (eds.). The 12th Symposium on the Geology of the Bahamas and Other Carbonate Regions. Gerace Research Center, San Salvador, Bahamas. Pp. 196-203.

Sloss, C.R., P. Hesp & M. Shepherd. 2012. Coastal dunes: Aeolian transport. Nature Education Knowledge 3: 21.

Space, J.C., B.M. Waterhouse, J.E. Miles, J. Tiobech, J & K. Rengulbai. 2003. Invasive Plant Species of Environmental Concern. U.S.D.A Forest Service Report to the Republic of Palau. Retrieved from http://www.hear.org/pier/pdf/palau_ report.pdf on February 20, 2013.

Spotila, J.R., E.A. Standora, S.J. Morreale& G.J. Ruiz. 1987. Temperature-dependent sex determination in the green turtle (Chelonia mydas): Effects on the sex-ratio on a natural beach. Herpetologica 43: 74–81.

Stewart, K.R. & P.H. Dutton. 2014. Breeding sex ratios in adult leatherback turtles (Dermochelys coriacea) may compensate for female-biased hatchling sex ratios. PLoS One 9: e88138.

Do you read IOTN online?

Tanaka, N. 2009. Vegetation bioshields for tsunami mitigation: review of effectiveness, limitations, construction, and sustainable management. Landscape and Ecological Engineering 5: 71-79.

Tani, C. & H. Sasakawa. 2006. Proline accumulates in Casuarina equisetifolia seedlings under salt stress. Soil Science and Plant Nutrition 52: 21-25.

Wheeler, G.S., G.S. Taylor, J.F. Gaskin & M.F. Purcell. 2011. Ecology and management of she-oak (Casuarina spp.), an invader of coastal Florida, U.S.A. Journal of Costal Research 27: 485- 492.

Whistler, A. W. & C.R. Elevitch. 2006. Casurina equisetifola (beach she-oak) C. cunninghamiana (river she-oak). Species Profiles for Pacific Island Agroforestry. 2 (I). Retrieved from http://www.agroforestry.net/tti/Casuarina-she-oak.pdf on December 16, 2012.

Witherington, B., S. Hirama & A. Mosier. 2011. Barriers to sea turtle nesting on Florida (United States) beaches: Linear extent and changes following storms. Journal of Coastal Research 27: 450-458.

Wood, A., D.T. Booth & C.J. Limpus. 2014. Sun exposure, nest temperature and loggerhead turtle hatchlings: Implications for beach shading management strategies at sea turtle rookeries. Journal of Experimental Marine Biology and Ecology 451: 105-114.

Zhang, L.H., S.J. Zhang, G.F. Ye, H.B. Shao, G.H. Lin & M. Brestic. 2013. Changes of tannin and nutrients during decomposition of branchlets of Casuarina equisetifolia plantation in subtropical coastal areas of China. Plant Soil Environment 59:74-79.