**Environmental Assessment and Aquatic Biodiversity Conservation of Amazonian Savannas, Marajó Island, Brazil**

Luciano Fogaça de A. Montag, Tiago Magalhães da S. Freitas, Ana Cristina Mendes-Oliveira and Ronaldo B. Barthem *Universidade Federal do Pará/Museu Paraense Emílio Goeldi Brazil* 

#### **1. Introduction**

260 Research in Biodiversity – Models and Applications

Schirone, B., Salis, A. & Vessella, F. (2011). Effectiveness of the Miyawaki method in

von Cräutlein, M., Korpelainen, H., Maria Pietiläinen, H. & Rikkinen, J. (2011). DNA

Ward, R.D., Zemlak, T.S., Innes, B.H., Last, P.R. & Hebert, P.D.N. (2005). DNA barcoding

Wilson, E.O. & Peter, F.M. (1986). *Biodiversity (Papers from the 1st National Forum on* 

Vol. 7, No. 1, (January 2011), pp. 81-92, ISSN 1860-188X.

360, No. 1462, (October 2005), pp. 1847–1857, ISSN 1471-2970.

(October 6, 1996), ISBN 978-0309037396, Washington DC, USA.

ISSN 1572-9710.

Mediterranean forest restoration programs. *Landscape and Ecological Engineering*,

barcoding: a tool for improved *taxon* identification and detection of species diversity. *Biodiversity and conservation*, Vol. 20, No. 2, (February 2011), pp. 373-389,

Australia's fish species. *Philosophical Transactions of the Royal Society, Series B*, Vol.

*Biodiversity, September 1986, Washington, D.C.)*, National Academy of Sciences

Marajó Island is located in the mouth of the Amazon River, the World's largest river, at its interface with the Atlantic Ocean (Goulding et al., 2003). Marajó is the World's largest riverine island (Cruz, 1987), with a total area of approximately fifty thousand square kilometers (Fig. 1). In addition to the Amazon, the island is also influenced by the Tocantins River and other small rivers of the south (Barthem & Schwassmann, 1994; UNEP, 2004).

The island is surrounded by sandy-clayey beaches, and encompasses a hydrographic system (rivers, channels, and creeks) which both drains and floods the *terra firme* forest and *várzeas*  (swamps) (Marques-Aguiar et al., 2002). In addition to these forest ecosystems, the island's lakes, lagoons, beaches, rivers, and mangroves contribute to its diversity of habitats and organisms (Marques-Aguiar et al., 2002; Montag et al., 2009; Almeida et al., 2009). This diversity of habitats influences the richness of the region's fauna, including its fish, and plays an important role in habitat preferences and use (Lowe-McConnell, 1999; Carrier et al., 2004). Most of these environments are heavily influenced by the inundation cycle of the estuarine region, which Junk (1997) characterizes as a polymodal cycle of low amplitude, but highly predictable flood pulses, influenced primarily by the local tides.

The climate of Marajó Island can be characterized by two categories of the Köppen classification system – Af (humid tropical, with mean precipitation in the driest month at least 60 mm) and Am, tropical monsoon, with excessive rainfall between February and May. During this period, two-thirds of the island are completely flooded (Cardoso & Pereira, 2002; Lima et al., 2005; Fig. 1). Annual precipitation on Marajó Island ranges between 2500 mm and 4000 mm, with a mean temperature of around 27ºC, and relative humidity of 81% to 94%. Rainfall is distributed in two distinct periods, with a marked rainy season between January and June, and a dry season, between September and November.

Despite this rigorous hydrological regime, the vegetation covering the part of the island that is flooded annually is referred to as a savanna (or flooded grassland; Fig. 2), which is known for the diversity and abundance of its fishery resources (Barthem & Fabré, 2003; Montag et al., 2009; Schaan, 2010). While the term savanna is more associated with specific floristic characteristics, comparable with those of the savannas of central Brazil (Eiten, 1972; Ratter et

Environmental Assessment and Aquatic Biodiversity

fig.). Photo by Miguel von Behr.

who produce a more marketable product (Schaan, 2010).

Conservation of Amazonian Savannas, Marajó Island, Brazil 263

Fig. 2. Aerial view of the Marajó landscape, with the savannas or grassland in lighter green (left fig.); a typical scenario of the savannas in the Marajó Island during the dry season (right

Humans have occupied Marajó Island for at least the past five to seven thousand years (Simões, 1981; Roosevelt et al., 1991). These first inhabitants probably subsisted on game, fish, and small-scale agriculture (Schaan, 2010), although, as in the present day, this activity would have been limited by the low fertility of the local soils and their inadequate drainage. However, these soils are appropriate for a number of native palm species, such as the buriti (*Mauritia flexuosa* L.), also known locally as miriti, and the açaí (*Euterpe oleracea* Mart.). These two plants provide the raw material on which much of the local economy is based. The buriti supplies a fiber used for the production of artifacts and household items, while the fruit of the açaí is the principal source of nutrients for much of the island's riverside population (Schaan, 2010). A third plant species, the wild nutmeg, *Virola surinamensis* (Rol.) Warb. provides the raw material for the local plywood industry (Homma et al., 1998), which is the principal source of income for many of the island's municipalities (Lima et al., 2005). Ranching, in particular of water buffalo, is another important source of income for the local inhabitants (Lima et al., 2005; Fig. 3). According to data from the Brazilian Institute for Geography and Statistics, IBGE (Barbosa, 2005), the Marajó stocks represent approximately one quarter of all the buffalo raised in Brazil. However, traditional ranching on the island has declined in recent years due to competition from cattle ranchers from southern Pará,

These economic activities, which are developed without conservation management guidelines, have contributed to the progressive degradation of the island's ecosystems. The shipping of *açaí* in motorized vessels also contributes to the contamination of the local rivers with oil and plastics, while the production of beef and pork leads to the silting up of bodies of water (Schaan, 2010). A number of authors have associated these anthropogenic impacts with the decline in the numbers of fish and species, and the abundance of fishery stocks (Ackermann, 1963; Smith, 2001, 2002). These stocks have also suffered direct impacts from overfishing, the use of gillnets of illegal mesh size, and the discarding of catches of

inadequate size or low market value (Hilbert, 1952; Barthem & Goulding, 2007).

Fig. 1. LandSat Image (2001) of Marajó Island in the Eastern Amazon. The eastern of the island shows the seasonally-flooded savannas (shaded pink).

al., 1997; Sanaiotti et al., 1997; Ribeiro & Walter, 1998, Barbosa et al., 2007), Harris (1980) and Schaan (2010) recognize the flooded grasslands of Marajó Island as a typical example of seasonally-flooded savanna, more typical of the Amazonian *várzeas*, given the duration of the flooding period. However, there are also important differences, especially in the dynamics of inundation. While the Marajó grasslands are inundated by rainwater, the floodplains of the lower Amazon basin are encroached by rising river levels (Sombroek, 1966). The influence of oceanic tides is an additional factor contributing to the unique ecology of the Marajó savannas (Moran, 1995), demanding specific adaptive responses from the living organisms that inhabit this environment.

*Brazil* 

Fig. 1. LandSat Image (2001) of Marajó Island in the Eastern Amazon. The eastern of the

al., 1997; Sanaiotti et al., 1997; Ribeiro & Walter, 1998, Barbosa et al., 2007), Harris (1980) and Schaan (2010) recognize the flooded grasslands of Marajó Island as a typical example of seasonally-flooded savanna, more typical of the Amazonian *várzeas*, given the duration of the flooding period. However, there are also important differences, especially in the dynamics of inundation. While the Marajó grasslands are inundated by rainwater, the floodplains of the lower Amazon basin are encroached by rising river levels (Sombroek, 1966). The influence of oceanic tides is an additional factor contributing to the unique ecology of the Marajó savannas (Moran, 1995), demanding specific adaptive responses from

island shows the seasonally-flooded savannas (shaded pink).

the living organisms that inhabit this environment.

Fig. 2. Aerial view of the Marajó landscape, with the savannas or grassland in lighter green (left fig.); a typical scenario of the savannas in the Marajó Island during the dry season (right fig.). Photo by Miguel von Behr.

Humans have occupied Marajó Island for at least the past five to seven thousand years (Simões, 1981; Roosevelt et al., 1991). These first inhabitants probably subsisted on game, fish, and small-scale agriculture (Schaan, 2010), although, as in the present day, this activity would have been limited by the low fertility of the local soils and their inadequate drainage. However, these soils are appropriate for a number of native palm species, such as the buriti (*Mauritia flexuosa* L.), also known locally as miriti, and the açaí (*Euterpe oleracea* Mart.). These two plants provide the raw material on which much of the local economy is based. The buriti supplies a fiber used for the production of artifacts and household items, while the fruit of the açaí is the principal source of nutrients for much of the island's riverside population (Schaan, 2010). A third plant species, the wild nutmeg, *Virola surinamensis* (Rol.) Warb. provides the raw material for the local plywood industry (Homma et al., 1998), which is the principal source of income for many of the island's municipalities (Lima et al., 2005).

Ranching, in particular of water buffalo, is another important source of income for the local inhabitants (Lima et al., 2005; Fig. 3). According to data from the Brazilian Institute for Geography and Statistics, IBGE (Barbosa, 2005), the Marajó stocks represent approximately one quarter of all the buffalo raised in Brazil. However, traditional ranching on the island has declined in recent years due to competition from cattle ranchers from southern Pará, who produce a more marketable product (Schaan, 2010).

These economic activities, which are developed without conservation management guidelines, have contributed to the progressive degradation of the island's ecosystems. The shipping of *açaí* in motorized vessels also contributes to the contamination of the local rivers with oil and plastics, while the production of beef and pork leads to the silting up of bodies of water (Schaan, 2010). A number of authors have associated these anthropogenic impacts with the decline in the numbers of fish and species, and the abundance of fishery stocks (Ackermann, 1963; Smith, 2001, 2002). These stocks have also suffered direct impacts from overfishing, the use of gillnets of illegal mesh size, and the discarding of catches of inadequate size or low market value (Hilbert, 1952; Barthem & Goulding, 2007).

Environmental Assessment and Aquatic Biodiversity

that may potentially be catalogued on Marajó Island.

Goeldi Museum in Belém.

(Barthem & Fabré, 2003).

(2009).

Conservation of Amazonian Savannas, Marajó Island, Brazil 265

and Selection of Priority Areas for the Conservation of the Amazonian Savannas of the Marajó Archipelago in the Brazilian State of Pará", which was financed by the Program for Biodiversity Research (PPBio) and the Brazilian Environment Ministry (MMA), through the

A total of 254 fish species were recorded from the flooded savannas of Marajó Island, including the first documentation of eight families for this region – Cetopsidae, Ctenoluciidae, Paralichthyidae, Poeciliidae, Polycentridae, Rivulidae, and Trichomycteridae (Montag et al., 2009; see Appendix 1). However, the bootstrap estimate of the region's total species richness was approximately 310 (Fig. 4), which represents an additional 50 species

Of these 254 species, 44 (17% of the total) are commercially important as food species, while 46 (18%) are targeted by the ornamental fish market. In fact, the marshlands of Marajó Island represent one of the most important fishing grounds of the lower Amazon basin

Fig. 4. Species accumulations curve for the number of fish species recorded in the Marajó savannas using the rarefaction technique and the species richness estimated by Bootstrap analysis for the data available for the period between 1905 and 2005. Source: Montag et al.

The principal species targeted by commercial fisheries include the tamuatá or brown hoplo (*Hoplosternum littorale*), thraira (*Hoplias malabaricus*), cangati or driftwood catfish (*Trachelyopterus galeatus*) and aracu or headstanders (family Anostomidae). The island's most popular ornamental fish include lebiasinids, caracids of the genera *Hemigrammus* and *Hyphessobrycon*, dwarf cichlids of the genera *Apistogramma*, *Crenicichla* and *Geophagus*, cascudos or plecos of the Loricariidae family, and stingrays of the genus *Potamotrygon*.

Fig. 3. The ranching of water buffaloes is an important source of income for the local inhabitants. Photo by Miguel von Behr.

Despite the unique features and ecological importance of Marajó Island in the local context, it has not been included in the environmental and hydrological management programs that have been developed for the Amazon region (Lima et al., 2005). One of the reasons for this is probably the lack of information on the region's fauna. Given this preoccupying scenario, this chapter focuses on the ecological evaluation of the fish diversity of the flooded savannas of Marajó Island in Brazil. The historical and biological aspects of the local ichthyofauna are analyzed, and the threats to this fauna are examined. The challenges for the implementation of effective conservation and management of one of the Amazon region's most important natural resources – its fish – are also discussed.

## **2. What do we know?**

## **2.1 The fishes**

Despite having one of the richest ichthyofaunas found anywhere on the planet (Reis et al., 2003), our scientific knowledge of the diversity of the fish of Marajó Island is restricted to just two studies, Boulenger (1897) and Montag et al. (2009), more than one hundred years apart. In the more recent study, Montag et al. (2009) revised the data available from fieldwork conducted between 2003 and 2005 in the municipalities of Chaves, Muaná, and Ponta de Pedras. Additional data were obtained from the ichthyological collections of the Goeldi Museum (MPEG) and the Museum of Zoology of São Paulo University (MZUSP) in Brazil, as well as international institutions, such as the Swedish Natural History Museum (NMR) and the Florida State Museum (UF, USA). Most of the specimens available in these collections were obtained during the 1980s and 1990s in the municipalities of Cachoeira do Arari, Muaná, Ponta de Pedras, Salvaterra, Santa Cruz do Arari, and Soure (Montag et al., 2009). This study was part of the PROBIO Marajó project entitled "Ecological Evaluation

Fig. 3. The ranching of water buffaloes is an important source of income for the local

Despite the unique features and ecological importance of Marajó Island in the local context, it has not been included in the environmental and hydrological management programs that have been developed for the Amazon region (Lima et al., 2005). One of the reasons for this is probably the lack of information on the region's fauna. Given this preoccupying scenario, this chapter focuses on the ecological evaluation of the fish diversity of the flooded savannas of Marajó Island in Brazil. The historical and biological aspects of the local ichthyofauna are analyzed, and the threats to this fauna are examined. The challenges for the implementation of effective conservation and management of one of the Amazon region's most important

Despite having one of the richest ichthyofaunas found anywhere on the planet (Reis et al., 2003), our scientific knowledge of the diversity of the fish of Marajó Island is restricted to just two studies, Boulenger (1897) and Montag et al. (2009), more than one hundred years apart. In the more recent study, Montag et al. (2009) revised the data available from fieldwork conducted between 2003 and 2005 in the municipalities of Chaves, Muaná, and Ponta de Pedras. Additional data were obtained from the ichthyological collections of the Goeldi Museum (MPEG) and the Museum of Zoology of São Paulo University (MZUSP) in Brazil, as well as international institutions, such as the Swedish Natural History Museum (NMR) and the Florida State Museum (UF, USA). Most of the specimens available in these collections were obtained during the 1980s and 1990s in the municipalities of Cachoeira do Arari, Muaná, Ponta de Pedras, Salvaterra, Santa Cruz do Arari, and Soure (Montag et al., 2009). This study was part of the PROBIO Marajó project entitled "Ecological Evaluation

inhabitants. Photo by Miguel von Behr.

natural resources – its fish – are also discussed.

**2. What do we know?** 

**2.1 The fishes** 

and Selection of Priority Areas for the Conservation of the Amazonian Savannas of the Marajó Archipelago in the Brazilian State of Pará", which was financed by the Program for Biodiversity Research (PPBio) and the Brazilian Environment Ministry (MMA), through the Goeldi Museum in Belém.

A total of 254 fish species were recorded from the flooded savannas of Marajó Island, including the first documentation of eight families for this region – Cetopsidae, Ctenoluciidae, Paralichthyidae, Poeciliidae, Polycentridae, Rivulidae, and Trichomycteridae (Montag et al., 2009; see Appendix 1). However, the bootstrap estimate of the region's total species richness was approximately 310 (Fig. 4), which represents an additional 50 species that may potentially be catalogued on Marajó Island.

Of these 254 species, 44 (17% of the total) are commercially important as food species, while 46 (18%) are targeted by the ornamental fish market. In fact, the marshlands of Marajó Island represent one of the most important fishing grounds of the lower Amazon basin (Barthem & Fabré, 2003).

Fig. 4. Species accumulations curve for the number of fish species recorded in the Marajó savannas using the rarefaction technique and the species richness estimated by Bootstrap analysis for the data available for the period between 1905 and 2005. Source: Montag et al. (2009).

The principal species targeted by commercial fisheries include the tamuatá or brown hoplo (*Hoplosternum littorale*), thraira (*Hoplias malabaricus*), cangati or driftwood catfish (*Trachelyopterus galeatus*) and aracu or headstanders (family Anostomidae). The island's most popular ornamental fish include lebiasinids, caracids of the genera *Hemigrammus* and *Hyphessobrycon*, dwarf cichlids of the genera *Apistogramma*, *Crenicichla* and *Geophagus*, cascudos or plecos of the Loricariidae family, and stingrays of the genus *Potamotrygon*.

Environmental Assessment and Aquatic Biodiversity

water to coastal areas.

Conservation of Amazonian Savannas, Marajó Island, Brazil 267

Data on precipitation and water levels are available from the website of the Brazilian National Waters Agency (Agência Nacional de Águas, or ANA). Rainfall is more intense during the first half of the year, between January and June, reaching a peak normally in March. The precipitation is not distributed homogeneously, and tends to be higher in the eastern and western portions of the island, and lower in its center (Lima et al., 2005). The highest precipitation – 200 mm in a single day – was recorded in the east of the island, the part closest to the Atlantic Ocean (Soure). The lowest precipitation rates coincide with the area of savanna, with the lowest values being recorded in September, when the monthly maximum is less than 100 mm (Cachoeira do Arari) (Fig. 5). The center of the island is flat and shallow, and the rainfall floods the savannas between March and May, forming permanent or temporary lakes and swamps (Fig. 6). In subsequent months, the local rivers drain off this

Fig. 5. Median monthly precipitation at different localities on Marajo Island (Source:

The tidal surge moves upstream into the Amazon from east to west, when it is deformed, delayed and amortized. The high tide increases the level of the river and dams or inverts its flow, which returns to normal during the ebb tide (Kosuth et al*.,* 1999). Rivers can be classified in three categories, according to the predominant hydrological force, i.e. river flow, tide or a combination of the two effects (Volker, 1966). The rivers of Marajó Island may be classified in all three categories. The rivers in the center of the island are affected only by local rainfall, while those on the coast are dominated by the tides, and those in intermediate areas are affected by a combination of these processes. The proximity of the ocean results in an

Brazilian National Waters Agency - ANA).

Until now, few endemic species have been recorded from the flooded savannas of Marajó Island, although this may be at least partly related to the deficiency of conclusive systematic and taxonomic studies for many species groups. One case in point here is swamp eel, *Synbranchus lampreia* Favorito, Zanata and Assumpção (2005), which is known only from the Goiapi River on Marajó Island. Given the gaps in our knowledge of the region's ichthyofauna and the unreliability of the taxonomic arrangements of most groups, Montag et al. (2009) proposed that the island should be considered among the regions with the highest priority for both biological inventories and the implementation of protected areas, based on well-defined empirical criteria.

### **2.2 Environmental patterns**

The savannas of Marajó Island are seasonally flooded by rain, forming a complex system of temporary or permanent lakes and swamps. The aquatic biodiversity of this region is adapted to the extreme conditions of drought and flood, together with high temperatures associated and low levels of dissolved oxygen (Almeida et al., 2009). The most common fish species found in these lakes and swamps are well adapted to the extremes of oxygen depletion (Kramer et al., 1978), such as the temporary development of a dermal lip protuberance for surface respiration (Winemiller, 1989) or permanent accessory respiratory organs, like the swimbladder of the pirarucu (*Arapaima gigas*) (Greenwood & Liem, 1984), and the vascularization of the posterior intestine in the tamuatá or brown hoplo (*Hoplosternum littorale*) (Persaud et al., 2006) or the oral mucosa in the poraquê or electric eel *Electrophorus electricus* as cited by Johansen et al. (1968).

The reproduction of these fish species is synchronized with the flood pulse. The electric eel (*Electrophorus electricus*) spawns during the late dry season, between September and December (Assunção & Schwassmann, 1995), while *Hoplosternun littorale* spawns at the beginning of the rainy season, i.e. January and February (Oliveira, 2000). This species builds nests in the flooded vegetation and presents parental care. For many fishes the environmental characteristics is an important factor for species distribution, and this is also applied for potamotrigonids stingrays. However, according to Almeida et al. (2009) the distribution of the stingray *Potamotrygon motoro* is related to body size, with the largest specimens being found in the center of the island, and the smaller individuals in peripheral areas.

Fishery activities are also synchronized with the flood pulse (Welcomme, 1979). The body of water expands during the rainy season, dispersing the fish populations over the floodplain, reducing fishery productivity. By contrast, during the dry season, the fish are restricted to isolated pools or shallow channels, facilitating their capture. Overall, 90% of the island's commercial catch is based on four species, with *Hoplosternum littorale* accounting for approximately two-thirds of total fishery production (Barthem & Goulding, 2007). Fishery activities are based on cast- and gillnetting. Gillnets are employed either in a fixed manner, or as a seine, which is drawn towards a beach or a second gillnet, which acts as a barrier. Hooks and harpoons are also used by artisanal fishermen (Albuquerque & Barthem, 2008).

#### **2.3 Pattern and process**

The flood pulse is the main ecological factor that determines the productivity and biological processes of the aquatic environments of the Amazon Basin (Junk et al., 1989; Junk & Wantzen, 2004). The flood pulse of the central portion of Marajó Island is determined basically by local precipitation levels, while water levels in marginal areas are determined primarily by tidal cycles.

266 Research in Biodiversity – Models and Applications

Until now, few endemic species have been recorded from the flooded savannas of Marajó Island, although this may be at least partly related to the deficiency of conclusive systematic and taxonomic studies for many species groups. One case in point here is swamp eel, *Synbranchus lampreia* Favorito, Zanata and Assumpção (2005), which is known only from the Goiapi River on Marajó Island. Given the gaps in our knowledge of the region's ichthyofauna and the unreliability of the taxonomic arrangements of most groups, Montag et al. (2009) proposed that the island should be considered among the regions with the highest priority for both biological inventories and the implementation of protected areas,

The savannas of Marajó Island are seasonally flooded by rain, forming a complex system of temporary or permanent lakes and swamps. The aquatic biodiversity of this region is adapted to the extreme conditions of drought and flood, together with high temperatures associated and low levels of dissolved oxygen (Almeida et al., 2009). The most common fish species found in these lakes and swamps are well adapted to the extremes of oxygen depletion (Kramer et al., 1978), such as the temporary development of a dermal lip protuberance for surface respiration (Winemiller, 1989) or permanent accessory respiratory organs, like the swimbladder of the pirarucu (*Arapaima gigas*) (Greenwood & Liem, 1984), and the vascularization of the posterior intestine in the tamuatá or brown hoplo (*Hoplosternum littorale*) (Persaud et al., 2006) or the oral mucosa in the poraquê or electric eel

The reproduction of these fish species is synchronized with the flood pulse. The electric eel (*Electrophorus electricus*) spawns during the late dry season, between September and December (Assunção & Schwassmann, 1995), while *Hoplosternun littorale* spawns at the beginning of the rainy season, i.e. January and February (Oliveira, 2000). This species builds nests in the flooded vegetation and presents parental care. For many fishes the environmental characteristics is an important factor for species distribution, and this is also applied for potamotrigonids stingrays. However, according to Almeida et al. (2009) the distribution of the stingray *Potamotrygon motoro* is related to body size, with the largest specimens being found in the

Fishery activities are also synchronized with the flood pulse (Welcomme, 1979). The body of water expands during the rainy season, dispersing the fish populations over the floodplain, reducing fishery productivity. By contrast, during the dry season, the fish are restricted to isolated pools or shallow channels, facilitating their capture. Overall, 90% of the island's commercial catch is based on four species, with *Hoplosternum littorale* accounting for approximately two-thirds of total fishery production (Barthem & Goulding, 2007). Fishery activities are based on cast- and gillnetting. Gillnets are employed either in a fixed manner, or as a seine, which is drawn towards a beach or a second gillnet, which acts as a barrier. Hooks and harpoons are also used by artisanal fishermen (Albuquerque & Barthem, 2008).

The flood pulse is the main ecological factor that determines the productivity and biological processes of the aquatic environments of the Amazon Basin (Junk et al., 1989; Junk & Wantzen, 2004). The flood pulse of the central portion of Marajó Island is determined basically by local precipitation levels, while water levels in marginal areas are determined

based on well-defined empirical criteria.

*Electrophorus electricus* as cited by Johansen et al. (1968).

center of the island, and the smaller individuals in peripheral areas.

**2.2 Environmental patterns** 

**2.3 Pattern and process** 

primarily by tidal cycles.

Data on precipitation and water levels are available from the website of the Brazilian National Waters Agency (Agência Nacional de Águas, or ANA). Rainfall is more intense during the first half of the year, between January and June, reaching a peak normally in March. The precipitation is not distributed homogeneously, and tends to be higher in the eastern and western portions of the island, and lower in its center (Lima et al., 2005). The highest precipitation – 200 mm in a single day – was recorded in the east of the island, the part closest to the Atlantic Ocean (Soure). The lowest precipitation rates coincide with the area of savanna, with the lowest values being recorded in September, when the monthly maximum is less than 100 mm (Cachoeira do Arari) (Fig. 5). The center of the island is flat and shallow, and the rainfall floods the savannas between March and May, forming permanent or temporary lakes and swamps (Fig. 6). In subsequent months, the local rivers drain off this water to coastal areas.

Fig. 5. Median monthly precipitation at different localities on Marajo Island (Source: Brazilian National Waters Agency - ANA).

The tidal surge moves upstream into the Amazon from east to west, when it is deformed, delayed and amortized. The high tide increases the level of the river and dams or inverts its flow, which returns to normal during the ebb tide (Kosuth et al*.,* 1999). Rivers can be classified in three categories, according to the predominant hydrological force, i.e. river flow, tide or a combination of the two effects (Volker, 1966). The rivers of Marajó Island may be classified in all three categories. The rivers in the center of the island are affected only by local rainfall, while those on the coast are dominated by the tides, and those in intermediate areas are affected by a combination of these processes. The proximity of the ocean results in an

Environmental Assessment and Aquatic Biodiversity

(Imhoff et al., 2000).

Conservation of Amazonian Savannas, Marajó Island, Brazil 269

depth (Santos, 2006) which, together with their habit of excavating holes in which they cool themselves during the dry season, provoke significant alterations in the structure of the superficial soil layers and the composition of the vegetation, which favor erosive processes (Dias, 1999; Fig. 7). In addition, the compaction of the soil creates an environment unfavorable for plant growth, reducing the productivity and longevity of forage species

Fig. 7. Water buffaloes cooling themselves during the dry season, which provokes significant alterations in the structure of the superficial soil layers and changes in the

Buffalo ranching also contributes with the nitrogen enrichment of water bodies through urine and feces, resulting in high turbidity and reduced oxygen levels. These alterations of hydrological resources may also affect the abundance and quality of fishery resources, as well as increasing the potential for the transmission of water-borne diseases. This process also affects the local biodiversity through the destruction of the vegetation, in which many

Most of the economic activities developed on Marajó Island provoke some form of impact on the local biota. Activities that result in deforestation, such as ranching, agriculture, and unregulated logging, result in the loss of riparian vegetation and the silting up of river beds (Goulding et al., 2003). The extraction of fruit-producing lumber species and the commercial exploitation of the palm-heart and fruit of the açaí result in a reduction in the abundance of fruit for many frugivorous animals, including fish (Barthem, 2001). While commercial fisheries are an extremely profitable activity in eastern Amazonia, they have been exerting increasing pressure on local fish stocks. Species such as the pirarucu *Arapaima gigas* and the tamuatá *Hoplosternum littorale* are being overfished, but are marketed prominently in the Ver-o-Peso market in Belém, the capital of the Brazilian state of Pará (Fig. 8). Commercial fishing by so-called "ice boats" (equipped with icebox), in particular in *várzea* lakes and

composition of the vegetation. Photo by Miguel von Behr.

species seek refuge when breeding (Bernardi, 2005).

increased intrusion of brackish water during the second half of the year, raising salinity levels near the coast and in the small rivers in the east of the island (Barthem & Schwassmann, 1994).

Fig. 6. Monthly variation in the water of the Cachoeira do Arari River, in the center of Marajó Island.

## **3. What are the threats to local biodiversity?**

Throughout its recent history, the Amazon basin has been subjected to a series of rapid processes of environmental degradation, which have had negative consequences for the local biota. On a broad scale, the principal economic activities that have contributed to this process have traditionally been cattle ranching and agriculture. However, logging and the harvesting of forest products, such as fruits, oils, latex, game, and fish, have also contributed to the depletion of natural resources. On Marajó Island, these processes have been typical of those observed in the rest of the Amazon basin. First occupied by Europeans in the 17th century, Marajó Island Marajó Island was involved in the principal economic cycles of the Amazon basin. During the colonial period, the island's principal economic activities were large-scale (by the standards of the period) cattle ranching, and the production of sugar, tobacco, and cotton in plantations established primarily in coastal locations (Teixeira, 1953; Miranda Neto, 1968). During this period, the trampling of the grasslands by the cattle already contributed to a decline in local fishery productivity (Brasil, 1990). Following a period of decadence, and the rubber boom at the turn of the twentieth century, ranching began to grow on Marajó Island in the 1920s, although it is currently in decline once again. Currently, ranching on the island is based on its herd of water buffalo, which arrived at the end of the 19th century, when animals of the Carabao breed, originally from the Phillipines (see Fig. 3). However, the weight of these animals results in hoofprints of up to 10 cm in

increased intrusion of brackish water during the second half of the year, raising salinity levels near the coast and in the small rivers in the east of the island (Barthem & Schwassmann, 1994).

Fig. 6. Monthly variation in the water of the Cachoeira do Arari River, in the center of

Throughout its recent history, the Amazon basin has been subjected to a series of rapid processes of environmental degradation, which have had negative consequences for the local biota. On a broad scale, the principal economic activities that have contributed to this process have traditionally been cattle ranching and agriculture. However, logging and the harvesting of forest products, such as fruits, oils, latex, game, and fish, have also contributed to the depletion of natural resources. On Marajó Island, these processes have been typical of those observed in the rest of the Amazon basin. First occupied by Europeans in the 17th century, Marajó Island Marajó Island was involved in the principal economic cycles of the Amazon basin. During the colonial period, the island's principal economic activities were large-scale (by the standards of the period) cattle ranching, and the production of sugar, tobacco, and cotton in plantations established primarily in coastal locations (Teixeira, 1953; Miranda Neto, 1968). During this period, the trampling of the grasslands by the cattle already contributed to a decline in local fishery productivity (Brasil, 1990). Following a period of decadence, and the rubber boom at the turn of the twentieth century, ranching began to grow on Marajó Island in the 1920s, although it is currently in decline once again. Currently, ranching on the island is based on its herd of water buffalo, which arrived at the end of the 19th century, when animals of the Carabao breed, originally from the Phillipines (see Fig. 3). However, the weight of these animals results in hoofprints of up to 10 cm in

**3. What are the threats to local biodiversity?** 

Marajó Island.

depth (Santos, 2006) which, together with their habit of excavating holes in which they cool themselves during the dry season, provoke significant alterations in the structure of the superficial soil layers and the composition of the vegetation, which favor erosive processes (Dias, 1999; Fig. 7). In addition, the compaction of the soil creates an environment unfavorable for plant growth, reducing the productivity and longevity of forage species (Imhoff et al., 2000).

Fig. 7. Water buffaloes cooling themselves during the dry season, which provokes significant alterations in the structure of the superficial soil layers and changes in the composition of the vegetation. Photo by Miguel von Behr.

Buffalo ranching also contributes with the nitrogen enrichment of water bodies through urine and feces, resulting in high turbidity and reduced oxygen levels. These alterations of hydrological resources may also affect the abundance and quality of fishery resources, as well as increasing the potential for the transmission of water-borne diseases. This process also affects the local biodiversity through the destruction of the vegetation, in which many species seek refuge when breeding (Bernardi, 2005).

Most of the economic activities developed on Marajó Island provoke some form of impact on the local biota. Activities that result in deforestation, such as ranching, agriculture, and unregulated logging, result in the loss of riparian vegetation and the silting up of river beds (Goulding et al., 2003). The extraction of fruit-producing lumber species and the commercial exploitation of the palm-heart and fruit of the açaí result in a reduction in the abundance of fruit for many frugivorous animals, including fish (Barthem, 2001). While commercial fisheries are an extremely profitable activity in eastern Amazonia, they have been exerting increasing pressure on local fish stocks. Species such as the pirarucu *Arapaima gigas* and the tamuatá *Hoplosternum littorale* are being overfished, but are marketed prominently in the Ver-o-Peso market in Belém, the capital of the Brazilian state of Pará (Fig. 8). Commercial fishing by so-called "ice boats" (equipped with icebox), in particular in *várzea* lakes and

Environmental Assessment and Aquatic Biodiversity

aquatic biota and many terrestrial animals.

directly (Bucher et al., 1993).

Salvaterra, and Soure.

Conservation of Amazonian Savannas, Marajó Island, Brazil 271

The native vegetation of Marajó Island has been modified by a combination of ranching, fires, and direct anthropogenic impacts (see Prance & Shaller 1982). Barthem (2001) considered the Marajó savannas to be the most threatened environment of the whole of the Amazon basin in terms of the conservation status of its ichthyofauna. In addition to these other anthropogenic pressures, this environment is being further threatened by the possible introduction of a new variety of rice developed specifically for the conditions on Marajó

One of the most dramatic anthropogenic impacts on the aquatic biota of the island's savannas was probably caused by the digging of the Tartaruga canal at the end of the 19th century. This canal crossed the savanna in a north-south direction for approximately 25 km, and was originally conceived as a means of reducing the time necessary to navigate between Macapá and Belém, the two principal cities on the Amazon estuary (Teixeira, 1953). The canal provoked the relatively rapid draining of the water accumulated in the savannas at the end of the rainy season (Ackermann, 1963), accentuating the effects of the dry season on the

In addition to all these threats to the local biodiversity, a large number of other projects are currently being planned or are under development in the Marajó region. One of these is the construction of a new canal, with the same objective of the Tartaruga canal, which is to reduce navigation time between Macapá and Belém. In addition to the intrinsic physical effects of the increase in the river-borne traffic, the degradation of aquatic habitats and the reduction or elimination of feeding resources will affect the plant and animal communities

The region has also been regional initiatives for the development of economic activities, including tourism, industrial fisheries, industrialized pineapple plantations, palm-heart processing plants, and cattle ranching. The Pará state government, through its Science, Technology, and Environment ministry (SECTAM), has implemented technical and scientific cooperation agreements, and other institutional covenants, with the aim of elaborating environmental management strategies for the sustainable development of all the island's municipalities which have instated official policies for the protection of the environment. Up to now, agreements have been signed with ten municipalities – Afuá, Anajás, Breves, Cachoeira do Arari, Chaves, Curralinho, Muaná, Ponta de Pedras,

Eleven of the 16 municipalities of Marajó Island have already obtained the seal of tourism quality from the Brazilian Tourism Agency (EMBRATUR), and are among the "flagships" of the tourism development program of the Pará State Tourism Company (PARATUR, 2001). The Marajó region is also included as a main hub in the Amazon Basin Ecotourism Development Program (PROECOTUR), a federal program administered by the Environment Ministry (MMA) through its secretary for Amazonian affairs, with financial support from the Inter-American Development Bank (BID). This program aims to promote the expansion of ecotourism in the Brazilian Amazon region, as one of the principal strategies for the

The first step towards the effective mitigation of any of the environmental impacts affecting the biodiversity of the flooded grasslands of Marajó Island is the consolidation of our

sustainable development of the nine states had make up the region.

**4. What do we still need to know?** 

Island by EMBRAPA, the agricultural research agency of the Brazilian government.

other sheltered areas of the estuary (bays, channels, and creeks), threatens the reproduction of commercial species, and thus their stocks over the long term (Goulding et al., 2003; UNEP, 2004). The negative consequences of this process may eventually throughout the local ecosystem in a cascade effect.

Fig. 8. The tamuatá *Hoplosternum littorale* are being marketed prominently in the Ver-o-Peso market in Belém, the capital of the Brazilian state of Pará. Read up on the broad "Large tamuatá from Marajó Island".

In addition to these impacts on the physical-chemical characteristics of the water and the vegetation, the compaction of the soil threatens the survival of the fish species that inhabit these seasonally-flooded habitats, such as the South American lungfish (*Lepidosiren paradoxa*), which may asphyxiate during the estivation period. During the dry season, the lungfish bury themselves in the humid soil of the savannas, covering themselves in mucous, which is produced in the tegument in large quantities to protect the animal from dehydration. They are also able to reduce their metabolism and body temperature in a process of estivation. There is an opening in the upper part of the mucous "cocoon", which allows the fish to breathe atmospheric air. The lungfish may remain in this state for many months, until the following rainy season, when more favorable conditions arise (Mesquita-Saad et al., 2002; Kramer et al., 1978).

In contrast with the fluctuations of the ranching industry, the harvesting of natural plant and animal resources has always been the mainstay of the economy of Marajó Island. The commercial exploitation of the fruit and palm-heart of the açaí, and fish stocks, constitute the most important economic activities for the local communities of the Amazon estuary (Brasil, 1990).

other sheltered areas of the estuary (bays, channels, and creeks), threatens the reproduction of commercial species, and thus their stocks over the long term (Goulding et al., 2003; UNEP, 2004). The negative consequences of this process may eventually throughout the

Fig. 8. The tamuatá *Hoplosternum littorale* are being marketed prominently in the Ver-o-Peso market in Belém, the capital of the Brazilian state of Pará. Read up on the broad "Large

In addition to these impacts on the physical-chemical characteristics of the water and the vegetation, the compaction of the soil threatens the survival of the fish species that inhabit these seasonally-flooded habitats, such as the South American lungfish (*Lepidosiren paradoxa*), which may asphyxiate during the estivation period. During the dry season, the lungfish bury themselves in the humid soil of the savannas, covering themselves in mucous, which is produced in the tegument in large quantities to protect the animal from dehydration. They are also able to reduce their metabolism and body temperature in a process of estivation. There is an opening in the upper part of the mucous "cocoon", which allows the fish to breathe atmospheric air. The lungfish may remain in this state for many months, until the following rainy season, when more favorable conditions arise (Mesquita-

In contrast with the fluctuations of the ranching industry, the harvesting of natural plant and animal resources has always been the mainstay of the economy of Marajó Island. The commercial exploitation of the fruit and palm-heart of the açaí, and fish stocks, constitute the most important economic activities for the local communities of the Amazon estuary

local ecosystem in a cascade effect.

tamuatá from Marajó Island".

Saad et al., 2002; Kramer et al., 1978).

(Brasil, 1990).

The native vegetation of Marajó Island has been modified by a combination of ranching, fires, and direct anthropogenic impacts (see Prance & Shaller 1982). Barthem (2001) considered the Marajó savannas to be the most threatened environment of the whole of the Amazon basin in terms of the conservation status of its ichthyofauna. In addition to these other anthropogenic pressures, this environment is being further threatened by the possible introduction of a new variety of rice developed specifically for the conditions on Marajó Island by EMBRAPA, the agricultural research agency of the Brazilian government.

One of the most dramatic anthropogenic impacts on the aquatic biota of the island's savannas was probably caused by the digging of the Tartaruga canal at the end of the 19th century. This canal crossed the savanna in a north-south direction for approximately 25 km, and was originally conceived as a means of reducing the time necessary to navigate between Macapá and Belém, the two principal cities on the Amazon estuary (Teixeira, 1953). The canal provoked the relatively rapid draining of the water accumulated in the savannas at the end of the rainy season (Ackermann, 1963), accentuating the effects of the dry season on the aquatic biota and many terrestrial animals.

In addition to all these threats to the local biodiversity, a large number of other projects are currently being planned or are under development in the Marajó region. One of these is the construction of a new canal, with the same objective of the Tartaruga canal, which is to reduce navigation time between Macapá and Belém. In addition to the intrinsic physical effects of the increase in the river-borne traffic, the degradation of aquatic habitats and the reduction or elimination of feeding resources will affect the plant and animal communities directly (Bucher et al., 1993).

The region has also been regional initiatives for the development of economic activities, including tourism, industrial fisheries, industrialized pineapple plantations, palm-heart processing plants, and cattle ranching. The Pará state government, through its Science, Technology, and Environment ministry (SECTAM), has implemented technical and scientific cooperation agreements, and other institutional covenants, with the aim of elaborating environmental management strategies for the sustainable development of all the island's municipalities which have instated official policies for the protection of the environment. Up to now, agreements have been signed with ten municipalities – Afuá, Anajás, Breves, Cachoeira do Arari, Chaves, Curralinho, Muaná, Ponta de Pedras, Salvaterra, and Soure.

Eleven of the 16 municipalities of Marajó Island have already obtained the seal of tourism quality from the Brazilian Tourism Agency (EMBRATUR), and are among the "flagships" of the tourism development program of the Pará State Tourism Company (PARATUR, 2001). The Marajó region is also included as a main hub in the Amazon Basin Ecotourism Development Program (PROECOTUR), a federal program administered by the Environment Ministry (MMA) through its secretary for Amazonian affairs, with financial support from the Inter-American Development Bank (BID). This program aims to promote the expansion of ecotourism in the Brazilian Amazon region, as one of the principal strategies for the sustainable development of the nine states had make up the region.

## **4. What do we still need to know?**

The first step towards the effective mitigation of any of the environmental impacts affecting the biodiversity of the flooded grasslands of Marajó Island is the consolidation of our

Environmental Assessment and Aquatic Biodiversity

any conservation efforts.

the state within which it is located.

**6. Conclusions** 

Conservation of Amazonian Savannas, Marajó Island, Brazil 273

One of the greatest challenges in the Amazon today is to integrate the exploitation of natural resources by the local human communities with the conservation of the biota. To achieve this, the economic, social, and ecological benefits of managed ecosystems must be understood by the local residents if there is to be any possibility of the sustainable use of resources. In the specific case of the savannas of Marajó Island, the understanding by residents and managers of the benefits of the conservation of these habitats for the maintenance or even the improvement of fishery stocks, will be essential for the success of

An important step towards the integration of local populations in any conservation scheme is the understanding of conservation initiatives, however minor or incipient, developed by the local populations themselves. However, conservation strategies should be diversified on both a local and regional scales due to the complexity of anthropogenic impacts and their differential effects on different trophic levels of ecosystems. Integrated conservation initiatives involving governments, non-governmental organizations, and in particular, the

In addition to the integrated management of natural resources, the creation of protected areas has been an important practical conservation strategy in Brazil. In fact, the whole of Marajó Island is located within a single state conservation unit, the Marajós Archipelago Environmental Protection Area, or Marajó EPA. Considered to be the largest state EPA in Brazil (MMA, 2007), this unit was created by article 13, paragraph 2 of the Pará state constitution, decreed on October 5th, 1989. However, this category of protected area is highly flexible in terms of the exploitation of natural resources and definitely does not guarantee the

The Marajó EPA was created as part of the ecological-economic zoning of the state of Pará, with the objectives of conserving the region's biodiversity, development and improvement of the quality of life of the island's population, the preservation of endangered species and representative areas of the local ecosystems, and the establishment of scientific, environmental education, and ecotourism projects. However, up to now, no management

An alternative proposal for the more effective conservation of the fauna and flora of Marajó Island would be the creation of a biosphere reserve. Biosphere reserves are areas of terrestrial and/or marine-coastal ecosystems recognized by the Man and the Biosphere Program (MaB), which was created in the 1970s by UNESCO, the United Nations Educational, Scientific and Cultural Organization. This program supports the development of a balanced relationship between people and nature, and determines that areas of special environmental and human value be recognized (designated) as biosphere reserves by the international coordinating council of the MaB program, at the request of the interested state. Following this recognition, the area of the reserve comes under the exclusive sovereignty of

The considerable lacunas in our current knowledge of the ichthyofauna of the region of Marajó Island indicate the need for more thorough, complementary surveys of the flooded grasslands (savannas) of the eastern portion of the island, studied by Montag et al. (2009), as well as new inventories of the western portion of the island. The anthropogenic impacts observed on local fish stocks, together with the dependence of local communities on the

active participation of local populations, should be given the highest priority.

maintenance of the ecological functions of the local ecosystems over the long term.

plan or administration program has been developed for this protected area.

knowledge of the ecological processes that underpin this unique system. However, few data are available in the literature on the status and integrity of local habitats and biodiversity, even in the case of the ichthyofauna, which is of direct interest to local human populations.

The 254 fish species already recorded on Marajó Island represent only 12% of the total diversity of the Amazon basin. Most of the records collated by Montag et al. (2009) were derived from sites located in the eastern portion of the island, and represent a relatively reduced sampling effort, considering its total area. Furthermore, the western portion of the island, with its many channels and tidal creeks, appears to be a more propitious environment for a high diversity of fish species. This part of the island is probably inhabited by a number of endemic species that are typical of the brackish estuarine and coastal systems that extend along the northern coast of South America, between the mouth of the Orinoco River in Venezuela and São Marcos Bay, in the Brazilian state of Maranhão.

The Amazon estuary is a unique, but still poorly-studied environment inhabited by both freshwater and marine fish species, many of which fundamental to both the regional and the national fishery industries (Barthem, 2001). The estuary and the adjacent vegetation constitute an extremely important nursery for the local ichthyofauna, providing both refuges and rich feeding resources for the juveniles of an ample variety of species. Many of these species also move through the flooded forest, where they eat fruits and seeds, and thus play an important role in the dispersal of the seeds of many *várzea* plant species (Gottsberger, 1978; Goulding, 1980; Kubitzki & Ziburski, 1994; Correa et al., 2007; Pollux, 2011).

As mentioned above, insufficient information is available on the composition of the region's ichthyofauna and the biology of the species that make up this fauna. At the present time, it is essential to conduct more definitive surveys, and to evaluate the status of populations and their long-term viability in both time and space, especially in the case of migratory species and/or those with an ample geographic range. In addition, understanding the basic functioning of the Amazonian ecosystems affected by seasonal flooding will be fundamentally important for the development of effective conservation strategies for the ichthyofauna of Marajó Island (Roberts, 1993).

## **5. Challenges: Applying what we already know**

The destruction and degradation of the rivers and creeks of the flooded savannas of Marajó Island, combined with the overfishing throughout the estuarine region, are the principal threats to the integrity of the local ichthyofauna. To be effective, any conservation strategy must take into consideration the complex life cycles of different species, and their specific habitat requirements. Given this, population-level studies will be essential for the understanding of the ecological niche of each species, so that more effective conservation strategies can be developed. Data on the habitat use of these species will also be essential for the development of effective *in situ* conservation strategies for target species.

In a wider context, the strategies applied to the conservation of species of special interest – such as the pirarucu or freshwater stingrays – will undoubtedly also favor most of the other species that share the same habitat or have similar niches. Unfortunately, far too few data are currently available for any such process to be systematic and dependable, although the identification of the key species and habitats may nevertheless provide an adequate baseline for the development of effective public policies for the conservation of the aquatic biodiversity of Marajó Island.

knowledge of the ecological processes that underpin this unique system. However, few data are available in the literature on the status and integrity of local habitats and biodiversity, even in the case of the ichthyofauna, which is of direct interest to local human populations. The 254 fish species already recorded on Marajó Island represent only 12% of the total diversity of the Amazon basin. Most of the records collated by Montag et al. (2009) were derived from sites located in the eastern portion of the island, and represent a relatively reduced sampling effort, considering its total area. Furthermore, the western portion of the island, with its many channels and tidal creeks, appears to be a more propitious environment for a high diversity of fish species. This part of the island is probably inhabited by a number of endemic species that are typical of the brackish estuarine and coastal systems that extend along the northern coast of South America, between the mouth of the

Orinoco River in Venezuela and São Marcos Bay, in the Brazilian state of Maranhão.

1980; Kubitzki & Ziburski, 1994; Correa et al., 2007; Pollux, 2011).

ichthyofauna of Marajó Island (Roberts, 1993).

biodiversity of Marajó Island.

**5. Challenges: Applying what we already know** 

The Amazon estuary is a unique, but still poorly-studied environment inhabited by both freshwater and marine fish species, many of which fundamental to both the regional and the national fishery industries (Barthem, 2001). The estuary and the adjacent vegetation constitute an extremely important nursery for the local ichthyofauna, providing both refuges and rich feeding resources for the juveniles of an ample variety of species. Many of these species also move through the flooded forest, where they eat fruits and seeds, and thus play an important role in the dispersal of the seeds of many *várzea* plant species (Gottsberger, 1978; Goulding,

As mentioned above, insufficient information is available on the composition of the region's ichthyofauna and the biology of the species that make up this fauna. At the present time, it is essential to conduct more definitive surveys, and to evaluate the status of populations and their long-term viability in both time and space, especially in the case of migratory species and/or those with an ample geographic range. In addition, understanding the basic functioning of the Amazonian ecosystems affected by seasonal flooding will be fundamentally important for the development of effective conservation strategies for the

The destruction and degradation of the rivers and creeks of the flooded savannas of Marajó Island, combined with the overfishing throughout the estuarine region, are the principal threats to the integrity of the local ichthyofauna. To be effective, any conservation strategy must take into consideration the complex life cycles of different species, and their specific habitat requirements. Given this, population-level studies will be essential for the understanding of the ecological niche of each species, so that more effective conservation strategies can be developed. Data on the habitat use of these species will also be essential for

In a wider context, the strategies applied to the conservation of species of special interest – such as the pirarucu or freshwater stingrays – will undoubtedly also favor most of the other species that share the same habitat or have similar niches. Unfortunately, far too few data are currently available for any such process to be systematic and dependable, although the identification of the key species and habitats may nevertheless provide an adequate baseline for the development of effective public policies for the conservation of the aquatic

the development of effective *in situ* conservation strategies for target species.

One of the greatest challenges in the Amazon today is to integrate the exploitation of natural resources by the local human communities with the conservation of the biota. To achieve this, the economic, social, and ecological benefits of managed ecosystems must be understood by the local residents if there is to be any possibility of the sustainable use of resources. In the specific case of the savannas of Marajó Island, the understanding by residents and managers of the benefits of the conservation of these habitats for the maintenance or even the improvement of fishery stocks, will be essential for the success of any conservation efforts.

An important step towards the integration of local populations in any conservation scheme is the understanding of conservation initiatives, however minor or incipient, developed by the local populations themselves. However, conservation strategies should be diversified on both a local and regional scales due to the complexity of anthropogenic impacts and their differential effects on different trophic levels of ecosystems. Integrated conservation initiatives involving governments, non-governmental organizations, and in particular, the active participation of local populations, should be given the highest priority.

In addition to the integrated management of natural resources, the creation of protected areas has been an important practical conservation strategy in Brazil. In fact, the whole of Marajó Island is located within a single state conservation unit, the Marajós Archipelago Environmental Protection Area, or Marajó EPA. Considered to be the largest state EPA in Brazil (MMA, 2007), this unit was created by article 13, paragraph 2 of the Pará state constitution, decreed on October 5th, 1989. However, this category of protected area is highly flexible in terms of the exploitation of natural resources and definitely does not guarantee the maintenance of the ecological functions of the local ecosystems over the long term.

The Marajó EPA was created as part of the ecological-economic zoning of the state of Pará, with the objectives of conserving the region's biodiversity, development and improvement of the quality of life of the island's population, the preservation of endangered species and representative areas of the local ecosystems, and the establishment of scientific, environmental education, and ecotourism projects. However, up to now, no management plan or administration program has been developed for this protected area.

An alternative proposal for the more effective conservation of the fauna and flora of Marajó Island would be the creation of a biosphere reserve. Biosphere reserves are areas of terrestrial and/or marine-coastal ecosystems recognized by the Man and the Biosphere Program (MaB), which was created in the 1970s by UNESCO, the United Nations Educational, Scientific and Cultural Organization. This program supports the development of a balanced relationship between people and nature, and determines that areas of special environmental and human value be recognized (designated) as biosphere reserves by the international coordinating council of the MaB program, at the request of the interested state. Following this recognition, the area of the reserve comes under the exclusive sovereignty of the state within which it is located.

## **6. Conclusions**

The considerable lacunas in our current knowledge of the ichthyofauna of the region of Marajó Island indicate the need for more thorough, complementary surveys of the flooded grasslands (savannas) of the eastern portion of the island, studied by Montag et al. (2009), as well as new inventories of the western portion of the island. The anthropogenic impacts observed on local fish stocks, together with the dependence of local communities on the

Environmental Assessment and Aquatic Biodiversity

*Hemigrammus* sp.

 *Hyphessobrycon* sp. *Metynnis luna* Cope, 1878

*Metynnis* sp.

*Moenkhausia* sp.

 *Phenacogaster* sp. *Poptella* sp.

*Roeboides* sp.

*Serrasalmus* sp.

 *Triportheus* sp. **Crenuchidae** 

**Ctenoluciidae** 

**Curimatidae** 

 *Hoplias* sp. **Gasteropelecidae**  *Carnegiella* sp.

 *Curimata* sp.1 *Curimata* sp.2 *Curimatopsis* sp.  **Erythrinidae** 

*Microcharacidium* sp.

*Hemigrammus levis* Durbin, 1908

 *Hemigrammus unilineatus* (Gill, 1858) *Hyphessobrycon heterorhabdus* (Ulrey, 1894)

 *Moenkhausia collettii* (Steindachner, 1882) *Moenkhausia lepidura* (Kner, 1858) *Moenkhausia pyrophthalma* Costa, 1994

*Paragoniates alburnus* Steindachner, 1876

 *Pristobrycon aureus* (Spix and Agassiz, 1829) *Pristobrycon calmoni* (Steindachner, 1908)

*Triportheus* aff. *angulatus* (Spix and Agassiz, 1829)

 *Erythrinus erythrinus* (Bloch and Schneider, 1801) *Hoplerythrinus unitaeniatus* (Spix and Agassiz)

*Triportheus angulatus* (Spix and Agassiz, 1829)

*Triportheus elongatus* (Günther, 1864)

*Crenuchus spilurus* Günther, 1863

*Boulengerella lucius* (Cuvier, 1816)

*Hoplias malabaricus* (Bloch, 1794)

*Curimata inornata* Vari, 1989

*Pristella maxillaris* (Ulrey, 1894)

 *Pygocentrus nattereri* Kner, 1858 *Roeboides myersii* Gill, 1870

 *Serrasalmus elongatus* Kner, 1858 *Serrasalmus rhombeus* (Linnaeus, 1766)

*Triportheus albus* Cope, 1872

 *Hemigrammus ocellifer* (Steindachner, 1882) *Hemigrammus rhodostomus* Ahl, 1924

Conservation of Amazonian Savannas, Marajó Island, Brazil 275

fishery resources of the Amazon estuary combine to make this region a priority for scientific studies of the aquatic biota and associated environments.

There is still a long way to go before the conservation of the aquatic biodiversity of Marajó Island can be assured and the maintenance of fishery stocks guaranteed over the long term. In both cases, management strategies must be well diversified. As part of this process, it will be the responsibility of the region's researchers to undertake scientific studies of local diversity (taxonomic revision with the identification of species and cataloguing of specimens), the relationships between species and the physical environment, spatial distribution of species, and the identification of possible endemics and key species for conservation. These studies will provide a theoretical and empirical database for the systematic development of public policies that integrate authorities, administrators, and local residents in the quest for the effective conservation and management of the natural resources of the aquatic environments of Marajó Island over the long term.

## **Appendix 1**

Fish species of the savannas of Marajó Island, Pará, Brazil. Modified from Montag et al. (2009).


fishery resources of the Amazon estuary combine to make this region a priority for scientific

There is still a long way to go before the conservation of the aquatic biodiversity of Marajó Island can be assured and the maintenance of fishery stocks guaranteed over the long term. In both cases, management strategies must be well diversified. As part of this process, it will be the responsibility of the region's researchers to undertake scientific studies of local diversity (taxonomic revision with the identification of species and cataloguing of specimens), the relationships between species and the physical environment, spatial distribution of species, and the identification of possible endemics and key species for conservation. These studies will provide a theoretical and empirical database for the systematic development of public policies that integrate authorities, administrators, and local residents in the quest for the effective conservation and management of the natural

Fish species of the savannas of Marajó Island, Pará, Brazil. Modified from Montag et al. (2009).

resources of the aquatic environments of Marajó Island over the long term.

studies of the aquatic biota and associated environments.

**Fish species from Marajó Island BELONIFORMES: Belonidae** 

*Potamorrhaphis* sp.

 *Acestrorhynchus* sp. **Anostomidae** 

*Leporinus* sp.

*Schizodon* sp.

*Bryconops* sp.

*Cheirodon* sp.

**Characidae** 

 *Leporinus affinis* Günther, 1864 *Leporinus fasciatus* (Bloch, 1794) *Leporinus friderici* (Bloch, 1794)

*Rhytiodus microlepis* Kner, 1858

*Schizodon fasciatus* Spix and Agassiz, 1829

*Schizodon vittatus* (Valenciennes, 1850)

 *Astyanax bimaculatus* (Linnaeus, 1758) *Bryconops alburnoides* Kner, 1858

*Charax pauciradiatus* (Günther, 1864)

 *Bryconops caudomaculatus* (Günther, 1864) *Bryconops giacopinii* ( Fernández-Yepez , 1950)

*Hemigrammus bellottii* (Steindachner, 1882)

*Potamorrhaphis guianensis* (Jardine, 1843)

**CHARACIFORMES: Acestrorhynchidae**  *Acestrorhynchus altus* Menezes, 1969 *Acestrorhynchus* cf. *altus* Menezes, 1969 *Acestrorhynchus falcatus* (Bloch 1794) *Acestrorhynchus falcirostris* (Cuvier, 1819) *Acestrorhynchus microlepis* (Schomburgk, 1841)

**Appendix 1** 

 *Hemigrammus levis* Durbin, 1908 *Hemigrammus ocellifer* (Steindachner, 1882) *Hemigrammus rhodostomus* Ahl, 1924 *Hemigrammus* sp. *Hemigrammus unilineatus* (Gill, 1858) *Hyphessobrycon heterorhabdus* (Ulrey, 1894) *Hyphessobrycon* sp. *Metynnis luna* Cope, 1878 *Metynnis* sp. *Moenkhausia collettii* (Steindachner, 1882) *Moenkhausia lepidura* (Kner, 1858) *Moenkhausia pyrophthalma* Costa, 1994 *Moenkhausia* sp. *Paragoniates alburnus* Steindachner, 1876 *Phenacogaster* sp. *Poptella* sp. *Pristella maxillaris* (Ulrey, 1894) *Pristobrycon aureus* (Spix and Agassiz, 1829) *Pristobrycon calmoni* (Steindachner, 1908) *Pygocentrus nattereri* Kner, 1858 *Roeboides myersii* Gill, 1870 *Roeboides* sp. *Serrasalmus elongatus* Kner, 1858 *Serrasalmus rhombeus* (Linnaeus, 1766) *Serrasalmus* sp. *Triportheus* aff. *angulatus* (Spix and Agassiz, 1829) *Triportheus albus* Cope, 1872 *Triportheus angulatus* (Spix and Agassiz, 1829) *Triportheus elongatus* (Günther, 1864) *Triportheus* sp. **Crenuchidae**  *Crenuchus spilurus* Günther, 1863 *Microcharacidium* sp. **Ctenoluciidae**  *Boulengerella lucius* (Cuvier, 1816) **Curimatidae**  *Curimata inornata* Vari, 1989 *Curimata* sp.1 *Curimata* sp.2 *Curimatopsis* sp.  **Erythrinidae**  *Erythrinus erythrinus* (Bloch and Schneider, 1801) *Hoplerythrinus unitaeniatus* (Spix and Agassiz) *Hoplias malabaricus* (Bloch, 1794) *Hoplias* sp. **Gasteropelecidae**  *Carnegiella* sp.

Environmental Assessment and Aquatic Biodiversity

 *Brachyhypopomus* sp. *Hypopomus* sp.

**Hypopomidae** 

*Hypopygus* sp.

 *Steatogenys* sp. **Rhamphichthyidae** 

 *Rhamphichthys* sp. **Sternopygidae** 

 *Eigenmannia* sp.1 *Eigenmannia* sp.2 *Rhabdolichops* sp.

*Sternopygus* sp.

**Osteoglossidae** 

*Centropomus* sp.

*Aequidens* sp.

 *Cichla* sp.1 *Cichla* sp.2

*Apistogramma* sp.

 *Chaetobranchopsis* sp. *Chaetobranchus* sp.

 **Cichlidae** 

Conservation of Amazonian Savannas, Marajó Island, Brazil 277

 *Brachyhypopomus brevirostris* (Steindachner, 1868) *Brachyhypopomus pinnicaudatus* (Hopkins, 1991)

*Microsternarchus bilineatus* Fernández-Yépez, 1968

*Hypopygus lepturus* Hoedeman, 1962

*Steatogenys elegans* (Steindachner, 1880)

 *Rhamphichthys marmoratus* Castelnau, 1855 *Rhamphichthys rostratus* (Linnaeus, 1766)

 *Distocyclus conirostris* (Eigenmann and Allen) *Eigenmannia humboldtii* (Steindachner, 1878)

*Sternopygus macrurus* (Bloch and Schneider, 1801)

*Rhabdolichops troscheli* (Kaup, 1856)

*Arapaima gigas* (Schinz, 1822)

**PERCIFORMES: Centropomidae** 

 *Acaronia nassa* (Heckel, 1840) *Aequidens pallidus* (Heckel, 1840)

**LEPIDOSIRENIFORMES: Lepidosirenidae**  *Lepidosiren paradoxa* Fitzinger, 1837 **OSTEOGLOSSIFORMES: Arapaimidae** 

*Osteoglossum bicirrhosum* (Cuvier, 1829)

*Apistogramma luelingi* Kullander, 1976

*Chaetobranchopsis orbicularis* (Steindachner, 1875)

 *Cichla melaniae* Kullander and Ferreira, 2006 *Cichla monoculus* Spix and Agassiz, 1831 *Cichla nigromaculata* Jardine, 1843 *Cichla ocellaris* Bloch and Schneider, 1801

*Astronotus ocellatus* (Agassiz, 1831)

 *Carnegiella strigata* (Günther, 1864) *Gasteropelecus sternicla* (Linnaeus, 1758) *Thoracocharax stellatus* (Kner, 1858) **Hemiodontidae**  *Hemiodus unimaculatus* (Bloch, 1794) **Lebiasinidae**  *Copella arnoldi* (Regan, 1912) *Copella nattereri* (Steindachner, 1876) *Nannostomus eques* Steindachner, 1876 *Nannostomus nittidus* Wetziman, 1978 *Pyrrhulina filamentosa* Valenciennes, 1847 **CLUPEIFORMES: Engraulididae**  *Anchovia* sp. *Anchovia surinamensis* (Bleeker, 1866) *Lycengraulis batesii* (Günther, 1868) *Lycengraulis* sp. *Pterengraulis atherinoides* (Linnaeus, 1766) **Pristigasteridae**  *Pellona castelnaeana* (Valenciennes, 1847) *Pellona flavipinnis* (Valenciennes, 1836) *Pellona* sp. **CYPRINODONTIFORMES: Anablepidae**  *Anableps microlepis* Muller and Troschel, 1844 **Poeciliidae**  *Pamphorichthys* sp. *Poecilia* sp.1 *Poecilia* sp.2 *Poecilia* sp.3 *Poecilia* sp.4 *Poecilia* sp.5  **Rivulidae**  *Rivulus* sp. **GYMNOTIFORMES: Apteronotidae**  *Adontosternarchus* sp. *Apteronotus albifrons* (Linnaeus, 1766) *Apteronotus* sp. *Sternarchella* cf. *terminalis* (Eigenmann and Allen, 1942) *Sternarchella* sp. *Sternarchogiton nattereri* (Steindachner, 1868) *Sternarchogiton porcinum* Eigenmann and Allen, 1942 *Sternarchogiton* sp. *Sternarchorhamphus muelleri* (Steindachner, 1881) *Sternarchorhamphus* sp. **Gymnotidae**  *Electrophorus electricus* (Linnaeus, 1766) *Gymnotus carapo* Linnaeus, 1758 *Gymnotus* sp.

#### **Hypopomidae**

276 Research in Biodiversity – Models and Applications

 *Carnegiella strigata* (Günther, 1864) *Gasteropelecus sternicla* (Linnaeus, 1758) *Thoracocharax stellatus* (Kner, 1858)

*Hemiodus unimaculatus* (Bloch, 1794)

 *Copella nattereri* (Steindachner, 1876) *Nannostomus eques* Steindachner, 1876 *Nannostomus nittidus* Wetziman, 1978 *Pyrrhulina filamentosa* Valenciennes, 1847

 *Anchovia surinamensis* (Bleeker, 1866) *Lycengraulis batesii* (Günther, 1868)

*Pterengraulis atherinoides* (Linnaeus, 1766)

 *Pellona castelnaeana* (Valenciennes, 1847) *Pellona flavipinnis* (Valenciennes, 1836)

**CYPRINODONTIFORMES: Anablepidae**  *Anableps microlepis* Muller and Troschel, 1844

**GYMNOTIFORMES: Apteronotidae** 

*Apteronotus albifrons* (Linnaeus, 1766)

*Sternarchogiton nattereri* (Steindachner, 1868)

 *Electrophorus electricus* (Linnaeus, 1766) *Gymnotus carapo* Linnaeus, 1758

*Sternarchella* cf. *terminalis* (Eigenmann and Allen, 1942)

*Sternarchogiton porcinum* Eigenmann and Allen, 1942

*Sternarchorhamphus muelleri* (Steindachner, 1881)

*Copella arnoldi* (Regan, 1912)

**CLUPEIFORMES: Engraulididae** 

**Hemiodontidae** 

**Lebiasinidae** 

*Anchovia* sp.

*Lycengraulis* sp.

**Pristigasteridae** 

*Pellona* sp.

**Poeciliidae** 

 *Pamphorichthys* sp. *Poecilia* sp.1 *Poecilia* sp.2 *Poecilia* sp.3 *Poecilia* sp.4 *Poecilia* sp.5  **Rivulidae**  *Rivulus* sp.

*Adontosternarchus* sp.

*Apteronotus* sp.

*Sternarchella* sp.

*Sternarchogiton* sp.

**Gymnotidae** 

*Gymnotus* sp.

*Sternarchorhamphus* sp.

 *Brachyhypopomus brevirostris* (Steindachner, 1868) *Brachyhypopomus pinnicaudatus* (Hopkins, 1991) *Brachyhypopomus* sp. *Hypopomus* sp. *Hypopygus lepturus* Hoedeman, 1962 *Hypopygus* sp. *Microsternarchus bilineatus* Fernández-Yépez, 1968 *Steatogenys elegans* (Steindachner, 1880) *Steatogenys* sp. **Rhamphichthyidae**  *Rhamphichthys marmoratus* Castelnau, 1855 *Rhamphichthys rostratus* (Linnaeus, 1766) *Rhamphichthys* sp. **Sternopygidae**  *Distocyclus conirostris* (Eigenmann and Allen) *Eigenmannia humboldtii* (Steindachner, 1878) *Eigenmannia* sp.1 *Eigenmannia* sp.2 *Rhabdolichops* sp. *Rhabdolichops troscheli* (Kaup, 1856) *Sternopygus macrurus* (Bloch and Schneider, 1801) *Sternopygus* sp. **LEPIDOSIRENIFORMES: Lepidosirenidae**  *Lepidosiren paradoxa* Fitzinger, 1837 **OSTEOGLOSSIFORMES: Arapaimidae**  *Arapaima gigas* (Schinz, 1822) **Osteoglossidae**  *Osteoglossum bicirrhosum* (Cuvier, 1829) **PERCIFORMES: Centropomidae**  *Centropomus* sp.  **Cichlidae**  *Acaronia nassa* (Heckel, 1840) *Aequidens pallidus* (Heckel, 1840) *Aequidens* sp. *Apistogramma luelingi* Kullander, 1976 *Apistogramma* sp. *Astronotus ocellatus* (Agassiz, 1831) *Chaetobranchopsis orbicularis* (Steindachner, 1875) *Chaetobranchopsis* sp. *Chaetobranchus* sp. *Cichla melaniae* Kullander and Ferreira, 2006 *Cichla monoculus* Spix and Agassiz, 1831 *Cichla nigromaculata* Jardine, 1843 *Cichla ocellaris* Bloch and Schneider, 1801 *Cichla* sp.1 *Cichla* sp.2

Environmental Assessment and Aquatic Biodiversity

*Potamotrygon* sp.

**Auchenipteridae** 

 *Ageneiosus* sp.1 *Ageneiosus* sp.2

*Asterophysus* sp.

 *Trachelyopterus* sp. **Callichthyidae** 

 **Cetopsidae**  *Cetopsis* sp. *Hemicetopsis* sp. **Doradidae**  *Acanthodoras* sp. *Anadoras* sp.

 *Doras* sp. *Hassar* sp.

**Heptapteridae** 

*Pimelodella* sp.

 *Rhamdia* sp.  *Insertae sedis* 

 **Loricariidae**  *Ancistrus* sp.1 *Ancistrus* sp.2

*Potamotrygon scobina* Garman, 1913

*Aspredinichthys filamentosus* (Valenciennes, 1840)

**SILURIFORMES: Aspredinidae** 

 *Aspredo aspredo* (Linnaeus, 1758) *Bunocephalus aleuropsis* Cope, 1870

*Ageneiosus inermis* (Linnaeus, 1766)

*Ageneiosus ucayalensis* Castelnau, 1855

 *Centromochlus heckelii* (De Filippi, 1853) *Pseudauchenipterus nodosus* (Bloch, 1794) *Tatia intermedia* (Steindachner, 1877) *Trachelyopterus galeatus* (Linnaeus, 1766)

 *Callichthys callichthys* (Linnaeus, 1758) *Hoplosternum littorale* (Hancock, 1828) *Megalechis personata* (Ranzini, 1841) *Megalechis thoracata* (Valenciennes, 1840)

*Doras eigenmanni* (Boulenger, 1895)

*Lithodoras dorsalis* (Valenciennes, 1840)

 *Pimelodella altipinnis* (Steindachner, 1864) *Pimelodella cristata* (Müller and Troschel, 1848) *Pimelodella gracilis* (Valenciennes, 1835)

*Rhamdia quelen* (Quoy and Gaimard, 1824)

*Phreatobius cisternarum* Goeldi, 1905

*Gladioglanis machadoi* Ferraris and Mago-Leccia, 1989

 *Auchenipterichthys longimanus* (Günther, 1864) *Auchenipterus nuchalis* (Spix and Agassiz, 1829)

Conservation of Amazonian Savannas, Marajó Island, Brazil 279

*Cichlasoma* sp.

*Crenicichla cincta* Regan, 1905

*Crenicichla macrophthalma* Heckel, 1840

 *Crenicichla notophthalmus* Regan, 1913 *Crenicichla regani* Ploeg, 1991

*Crenicichla reticulata* Heckel, 1840

*Crenicichla* sp.1

*Crenicichla* sp.2

*Crenicichla* sp.3

*Crenicichla strigata* Günther, 1862

*Geophagus camopiensis* Pellegrin, 1903

*Geophagus* sp.

*Geophagus surinamensis* (Bloch, 1791)

*Satanoperca jurupari* (Heckel, 1840)

#### **Gobiidae**

*Awaous flavus* (Valenciennes, 1837)

*Bathygobius* sp.

*Eleotris* sp.

*Evorthodus* sp.

*Gobioides* sp.

*Gobionellus* sp.

#### **Mugilidae**

*Mugil curema* Valenciennes, 1836

#### **Polycentridae**

 *Monocirrhus polyacanthus* Heckel, 1840 *Polycentrus schomburgkii* Müller and Troschel, 1848

#### **Sciaenidae**

*Cynoscion microlepidotus* (Cuvier, 1830)

*Cynoscion* sp.

 *Macrodon ancylodon* (Bloch and Schneider, 1801) *Pachypops fourcroi* (Lacepède, 1802)

*Pachypops* sp.

 *Pachypops trifilis* (Müller and Troschel, 1849) *Plagioscion auratus* (Castelnau, 1855)

*Plagioscion* sp.

 *Plagioscion squamosissimus* (Heckel, 1840) *Plagioscion surinamensis* (Bleeker, 1973)

#### **PLEURONECTIFORMES: Achiridae**

 *Achirus achirus* (Linnaeus, 1758) *Achirus* sp.

**Paralichthyidae** 

 *Paralichthys brasiliensis* (Ranzani, 1842) *Paralichthys* sp.

#### **RAJIFORMES: Potamotrygonidae**

 *Potamotrygon motoro* (Müller and Henle, 1841) *Potamotrygon orbignyi* (Castelnau, 1855)

*Cichla temensis* Humboldt, 1821

*Crenicichla cincta* Regan, 1905

 *Crenicichla regani* Ploeg, 1991 *Crenicichla reticulata* Heckel, 1840

 *Crenicichla strigata* Günther, 1862 *Geophagus camopiensis* Pellegrin, 1903

 *Geophagus surinamensis* (Bloch, 1791) *Satanoperca jurupari* (Heckel, 1840)

*Awaous flavus* (Valenciennes, 1837)

*Mugil curema* Valenciennes, 1836

*Monocirrhus polyacanthus* Heckel, 1840

*Cynoscion microlepidotus* (Cuvier, 1830)

*Pachypops fourcroi* (Lacepède, 1802)

*Plagioscion auratus* (Castelnau, 1855)

*Polycentrus schomburgkii* Müller and Troschel, 1848

*Macrodon ancylodon* (Bloch and Schneider, 1801)

*Pachypops trifilis* (Müller and Troschel, 1849)

 *Plagioscion squamosissimus* (Heckel, 1840) *Plagioscion surinamensis* (Bleeker, 1973) **PLEURONECTIFORMES: Achiridae**  *Achirus achirus* (Linnaeus, 1758)

*Paralichthys brasiliensis* (Ranzani, 1842)

 *Potamotrygon motoro* (Müller and Henle, 1841) *Potamotrygon orbignyi* (Castelnau, 1855)

**RAJIFORMES: Potamotrygonidae** 

 *Crenicichla macrophthalma* Heckel, 1840 *Crenicichla notophthalmus* Regan, 1913

*Cichlasoma* sp.

 *Crenicichla* sp.1 *Crenicichla* sp.2 *Crenicichla* sp.3

*Geophagus* sp.

 *Bathygobius* sp. *Eleotris* sp. *Evorthodus* sp. *Gobioides* sp. *Gobionellus* sp. **Mugilidae** 

 **Polycentridae** 

 **Sciaenidae** 

*Cynoscion* sp.

*Pachypops* sp.

*Plagioscion* sp.

 *Achirus* sp. **Paralichthyidae** 

*Paralichthys* sp.

 **Gobiidae** 

 *Potamotrygon scobina* Garman, 1913 *Potamotrygon* sp. **SILURIFORMES: Aspredinidae**  *Aspredinichthys filamentosus* (Valenciennes, 1840) *Aspredo aspredo* (Linnaeus, 1758) *Bunocephalus aleuropsis* Cope, 1870 **Auchenipteridae**  *Ageneiosus inermis* (Linnaeus, 1766) *Ageneiosus* sp.1 *Ageneiosus* sp.2 *Ageneiosus ucayalensis* Castelnau, 1855 *Asterophysus* sp. *Auchenipterichthys longimanus* (Günther, 1864) *Auchenipterus nuchalis* (Spix and Agassiz, 1829) *Centromochlus heckelii* (De Filippi, 1853) *Pseudauchenipterus nodosus* (Bloch, 1794) *Tatia intermedia* (Steindachner, 1877) *Trachelyopterus galeatus* (Linnaeus, 1766) *Trachelyopterus* sp. **Callichthyidae**  *Callichthys callichthys* (Linnaeus, 1758) *Hoplosternum littorale* (Hancock, 1828) *Megalechis personata* (Ranzini, 1841) *Megalechis thoracata* (Valenciennes, 1840) **Cetopsidae**  *Cetopsis* sp. *Hemicetopsis* sp. **Doradidae**  *Acanthodoras* sp. *Anadoras* sp. *Doras eigenmanni* (Boulenger, 1895) *Doras* sp. *Hassar* sp. *Lithodoras dorsalis* (Valenciennes, 1840) **Heptapteridae**  *Gladioglanis machadoi* Ferraris and Mago-Leccia, 1989 *Pimelodella altipinnis* (Steindachner, 1864) *Pimelodella cristata* (Müller and Troschel, 1848) *Pimelodella gracilis* (Valenciennes, 1835) *Pimelodella* sp. *Rhamdia quelen* (Quoy and Gaimard, 1824) *Rhamdia* sp.  *Insertae sedis Phreatobius cisternarum* Goeldi, 1905 **Loricariidae**  *Ancistrus* sp.1 *Ancistrus* sp.2

Environmental Assessment and Aquatic Biodiversity

*Geografia*, Vol.25, pp. 273-276, ISSN 0034-723X

**8. References** 

8122

0077-2232

91-865510-01-0

Brazil, 2002

Conservation of Amazonian Savannas, Marajó Island, Brazil 281

Ackermann, F.L. (1963). O lago Arari da ilha de Marajó e seus problemas. *Revista Brasileira de* 

Albuquerque, A.A. & Barthem, R.B. (2008). A pesca do tamoatá *Hoplosternum littorale*

Almeida, M.P.; Barthem, R.B.; Viana, A.S.; Charvet-Almeida, P. (2009). Factors affecting the

Assunção, M.I.S. & Schwassmann, H. (1995). Reproduction and larval development of

Barbosa, N.G.S. (2005). Bubalinocultura no Estado do Pará. *Revista Brasileira de Reprodução* 

Barbosa, R.I.; Campos, C.; Pinto, F.; Fearnside, P.M. (2007). The "Lavrados" of Roraima:

Barthem, R.B. & Fabré, N.N. (2003). Biologia e diversidade dos recursos pesqueiros da

Barthem, R.B. & Schwassmann, H.O. (1994). Amazon river influence on the seasonal

Barthem, R.B. (2001). Componente Biota Aquática, In: *Biodiversidade na Amazônia Brasileira*,

Boulenger, G.A. (1897). On a collection of fishes from the island of Marajó, Brazil. *Annals and* 

Brasil, República Federativa do Brasil. (1990). *Censos econômicos 1985 - Censo agropecuário*,

Bucher, E.; Bonetto, A.; Boyle, T.; Canevari, P.; Castro, G.; Huszar, P.; Stone, T. (1993).

Cardoso, E.C. & Pereira, W.L.A. (2002). *Mineral deficiency of buffaloes from Marajó Island, North* 

(Eds.), 60-78, Câmara do Livro, São Paulo, Brazil, ISBN 85-85994-13-4 Bernardi, C.C. (2005). *Conflitos sócio-ambientais decorrentes da bubalinocultura em territórios* 

(Ed.), 11-55, Pro-Várzea, Manaus, Amazonas, Brazil, ISBN 85-7401-124-X Barthem, R.B. & Golding, M. (2007). *An Unexpected Ecosystem: The Amazon revealed by the* 

*Journal of Aquatic Sciences*, Vol.4, No.1, pp. 1-11, ISSN 1809-9009

*Freshwaters*, Vol.6, No.2, pp. 175-184, ISSN 0936-9902

Garden Press, Lima, Peru, ISBN 978-9972-2912-4-1.

Universidade Católica de Brasília, Brasília, Brazil

*Magazine of Natural History*, Vol.20, No.117, pp. 294-299

*Ecosystems & Communities*, Vol.1, pp. 29-41, ISSN 1749-0502

*Animal*, Vol.29, No.1, pp. 34-38, ISSN 0102-0803

(Hancock, 1828) (Siluriformes: Callichthyidae) na ilha de Marajó. *Boletim do Museu Paraense Emílio Goeldi*, série Ciências Humanas, Vol.3, No.3, pp. 359-372, ISSN 1981-

distribution and abundance of freshwater stingrays (Chondrichthyes: Potamotrygonidae) at Marajó Island, mouth of the Amazon River. *Pan-American* 

*Electrophorus electricus* on Marajó Island (Pará, Brazil). *Ichthyological Exploration of* 

Biodiversity and Conservation of Brazil's Amazonian Savannas. *Functional* 

Amazônia, In: *A pesca e os recursos pesqueiros na Amazônia brasileira*, M.L., Rufino

*fisheries*, Lima Amazon Conservation Association (ACA) and Missouri Botanical

displacement of the salt wedge in the Tocantins river estuary, Brazil, 1983-1985. *Boletim do Museu Paraense Emílio Goeldi*, série Zoologia, Vol.10, pp. 119-130, ISSN

J.P.R. Capobianco, A. Veríssimo, A. Moreira, D. Sawyer, I. Santos and L.P. Pinto

*pesqueiros artesanais*: *o caso Olinda Nova do Maranhão*, Mastering Dissertation,

Fundação Instituto Brasileiro de Geografia e Estatística (IBGE), Rio de Janeiro, No.1

*Hidrovia: Un examen ambiental inicial de la via fluvial Paraguay-Parana*, Humedales para Las Americas, Manomet, Mass, USA and Buenos Aires, Argentina, ISBN ISBN

*of Brazil: current situation and perspectives*, I Buffalo Symposium of Americas, Belém,

 *Chaetostoma* sp. *Farlowella* aff. *knerii* (Steindachner, 1882) *Farlowella amazona* (Gunther, 1864) *Farlowella* sp. *Hemiancistrus* sp. *Hemiodontichthys acipenserinus* (Kner, 1853) *Hemiodontichthys* sp. *Hypoptopoma* sp. *Hypostomus* sp. *Lasiancistrus* sp. *Limatulichthys* sp. *Liposarcus pardalis* (Castelnau, 1855) *Loricaria catphracta* Linnaeus, 1758 *Panaque* sp. *Pseudoloricaria* sp. *Pterygoplichthys* sp. *Reganella* sp. **Pimelodidae**  *Brachyplatystoma vaillantii* (Valenciennes, 1840) *Hypophthalmus marginatus* Valenciennes, 1840 *Pimelodus blochii* Valenciennes, 1840 *Pimelodus ornatus* Kner, 1858 *Pimelodus* sp.1 *Pimelodus* sp.2 *Pinirampus pirinampu* (Spix and Agassiz, 1829) *Zungaro zungaro* (Humboldt, 1821) **Pseudopimelodidae**  *Batrochoglanis raninus* (Valenciennes, 1840) **Trichomycteridae**  *Henonemus taxistigmus* (Fowler, 1814) **SYNBRANCHIFORMES: Synbranchidae**  *Synbranchus lampreia* Favorito, Zanata and Assumpção, 2005 *Synbranchus marmoratus* Bloch, 1795 *Synbranchus* sp. **TETRAODONTIFORMES: Tetraodontidae**  *Colomesus asellus* (Müller and Troschel, 1849) *Colomesus psittacus* (Bloch and Schneider, 1801)

#### **7. Acknowledgments**

We are grateful to the PROBIO program (Project for the Conservation and Sustainable Use of Biological Diversity) of the Brazilian Environment Ministry, which is subsidized by the Global Environment Facility (GEF), which financed the PROBIO Marajó project. We are also grateful to Mr. Miguel von Behr for providing the pictures that make up this work and Dr. Stephen Ferrari for his help in correcting text, particularly the english. Finally, we dedicate this paper to the memory of the coordinator of the PROBIO Marajó project, Samuel Almeida.

## **8. References**

280 Research in Biodiversity – Models and Applications

*Chaetostoma* sp.

 *Farlowella* sp. *Hemiancistrus* sp.

 *Panaque* sp. *Pseudoloricaria* sp. *Pterygoplichthys* sp. *Reganella* sp. **Pimelodidae** 

 *Pimelodus* sp.1 *Pimelodus* sp.2

**Pseudopimelodidae** 

**Trichomycteridae** 

*Synbranchus* sp.

**7. Acknowledgments** 

Almeida.

 *Hemiodontichthys* sp. *Hypoptopoma* sp. *Hypostomus* sp. *Lasiancistrus* sp. *Limatulichthys* sp.

 *Farlowella* aff. *knerii* (Steindachner, 1882) *Farlowella amazona* (Gunther, 1864)

*Hemiodontichthys acipenserinus* (Kner, 1853)

 *Brachyplatystoma vaillantii* (Valenciennes, 1840) *Hypophthalmus marginatus* Valenciennes, 1840

*Pinirampus pirinampu* (Spix and Agassiz, 1829)

*Synbranchus lampreia* Favorito, Zanata and Assumpção, 2005

We are grateful to the PROBIO program (Project for the Conservation and Sustainable Use of Biological Diversity) of the Brazilian Environment Ministry, which is subsidized by the Global Environment Facility (GEF), which financed the PROBIO Marajó project. We are also grateful to Mr. Miguel von Behr for providing the pictures that make up this work and Dr. Stephen Ferrari for his help in correcting text, particularly the english. Finally, we dedicate this paper to the memory of the coordinator of the PROBIO Marajó project, Samuel

*Batrochoglanis raninus* (Valenciennes, 1840)

 *Liposarcus pardalis* (Castelnau, 1855) *Loricaria catphracta* Linnaeus, 1758

 *Pimelodus blochii* Valenciennes, 1840 *Pimelodus ornatus* Kner, 1858

*Zungaro zungaro* (Humboldt, 1821)

 *Henonemus taxistigmus* (Fowler, 1814) **SYNBRANCHIFORMES: Synbranchidae** 

*Synbranchus marmoratus* Bloch, 1795

**TETRAODONTIFORMES: Tetraodontidae**  *Colomesus asellus* (Müller and Troschel, 1849) *Colomesus psittacus* (Bloch and Schneider, 1801)


Environmental Assessment and Aquatic Biodiversity

127

Conservation of Amazonian Savannas, Marajó Island, Brazil 283

Junk, W.J.; Bayley, P.B.; Sparks, R.E. (1989). The flood pulse concept in river-floodplain

Kosuth, P.; Callède, J.; Laraque, A.; Filizola, N.; Guyot, J.L.; Seyler, P.; Fritsh, J.M. (1999).

patterns. *Canadian Journal of Zoology*, Vol.56, pp. 719-729, ISSN 0008-4301 Kubitzki, K. & Ziburski, A. (1994). Seed dispersal in flood plain forests of Amazonia.

Lima, A.M.M.; Oliveira, L.L.; Fontinhas, R.L.; Lima, R.J.S. (2005). Ilha do Marajó: revisão

Lowe-McConnell, R.H. (1999). *Estudos ecológicos de comunidades de peixes tropicais*, EDUSP,

Marques-Aguiar, S.A.; Melo, C.C.S.; Aguiar, G.F.S.; Queiróz, G.A.L. (2002). Levantamento

Miranda Neto, M.J. (1968). *A Foz do Rio-Mar, Subsídios Para o Desenvolvimento de Marajó*.

MMA, Ministério do Meio Ambiente. (2007). *Unidades de Conservação do Brasil*, Secretaria de

Montag, L.F.A., Albuquerque, A.A., Freitas, T.M.S.; Barthem, R.B. (2009). The Ichthyofauna

Moran, E.F. (1995). Rich and poor ecosystems of Amazonia: an approach to management, In:

Oliveira, J.C.S. (2000). *Ecologia e reprodução do tamuatá,* Hoplosternum littorale *Hancok, 1828* 

Persaud, D.I.; Ramnarine, I.W.; Agard, J.B.R. (2006). Ontogeny of the alimentary canal and

Pollux, B.J.A. (2011). The experimental study of seed dispersal by fish (ichthyochory).

Prance, G.T. & Schaller, G.B. (1982). Preliminary study of some vegetation types of the Pantanal, Mato Grosso, Brazil. *Brittonia*, Vol.34, pp. 228-251, ISSN 0007-196X

*Freshwater Biology*, Vol.56, pp. 197–212, ISSN 0046-5070

*Revista Brasileira de Zoologia*, Vol.19, No.3, pp. 841-854, ISSN 0101-8175 Mesquita-Saad, L.S.B.; Leitão, M.A.B.; Paula-Silva, M.N.; Chippari-Gomes, A.R.; Almeida-

*Biotropica*, Vol.26, pp. 30–43, ISSN 0006-3606

São Paulo, Brazil, ISBN 85-314-0493-2

*Environment*, Vol.5, No.1, pp. 65-80, ISSN 1519-8634

*of Biology*, Vol.62, No.3, pp. 495-501, ISSN 1678-4375

Biodiversidade e Florestas/MMA, Brasília, Brazil

Distribuidora Record, Rio de Janeiro, Brazil

New York, USA, ISBN 92-808-0877-X

Grande do Norte, Brazil

1909

ISSN 1676-0611

systems. In: Proceedings of International Large River Symposium, D.P. Dodge (Ed.), *Canadian Special Publication of Fisheries and Aquatic Sciences*, Vol.106, pp. 110-

Influence de la marée océanique sur le cours aval de l'Amazone. *Hydrological and Geochemical Processess in Large Scale River Basins,* Manaus, Amazonas, Brazil, 1999 Kramer, D.L.; Lindsey, C.C.; Moodie, G.E.E.; Stevens, E.D. (1978). The fishes and the aquatic

environment of the central Amazon basin, with particular reference to respiratory

histórica, hidroclimatologia, bacias hidrográficas e proposta de gestão. *Holos* 

preliminar da mastofauna da região de Anajás-Muaná, Ilha de Marajó, Pará, Brasil.

Val, V.M.F. (2002). Especialização e supressão metabólicas durante períodos de estivação do peixe pulmonado sul-americano. *Lepidosiren paradoxa*. *Brazilian Journal* 

of Savannas from Marajó Island, State of Pará, Brazil. *Biota Neotropica*, Vol.9, No.3,

*The Fragile Tropics of Latin American: Sustainable Management of Changing Environments*, T. Nishizawa and J.I. Uitto (Eds.), United Nations University Press,

*(Osteichthyes: Siluriformes: Callichthyidae), da área de proteção ambiental do rio Curiaú, Macapá-AP*. Doctor Thesis, Universidade Federal do Rio Grande do Norte, Rio

respiratory physiology of larval *Hoplosternum littorale* (Hancock, 1828): an intestinal air-breathing teleost. *Environmental Biology of Fishes*. Vol.76, pp. 37-45, ISSN 0378-


Carrier, J.C.; Pratt, H.L.; Castro, J.I. (2004). Reproductive biology of elasmobranchs, In:

Correa, S.B.; Winemiller, K.O.; López-Fernández, H.; Galetti, M. (2007). Evolutionary

Dias, M.C.O. (Ed). (1999). *Manual de impactos ambientais: orientações básicas sobre aspectos ambientais de atividades produtivas*, Banco do Nordeste, Fortaleza, Ceará, Brazil Eiten, G. (1972). The cerrado vegetation of Brazil. *Botanical Review*, Vol.38, pp. 201-341, ISSN

Favorito, S.E.; Zanata, A.M.; Assumpção, M.I. (2005). A new *Synbranchus* (Teleostei:

Gottsberger, G. (1978). Seed dispersal by fish in the inundated regions of Humaita,

Goulding, M. (1980). *The Fishes and the Forest: Explorations in Amazonian Natural History*, University of California Press, Berkeley, California, USA, ISBN 0-520-04131-3 Goulding, M.; Barthem, R.B.; Ferreira, E. (2003). *The Smithsonian atlas of the Amazon*,

Greenwood, P.H. & Liem, K.F. (1984) Aspiratory respiration in *Arapaima gigas* (Teleostei,

Harris, D.R. (1980) Tropical savanna environments: Definition, distribution, diversity, and

Hilbert, P.P. (1952) Contribuição à Arqueologia da Ilha de Marajó: Os Tesos Marajoaras do

Homma, A.K.O.; Conto, A.J.; Ferreira, C.A.P.; Carvalho, R.A.; Walker, R.T. (1998). A

Imhoff, S.; Silva, A.P.; Tormena, C.A. (2000). Aplicações da curva de resistência no controle

Johansen, K.; Lenfant, C.; Schmidt-Nielsen, K. (1968). Gas exchange and control of breathing

Junk, W.J. & Wantzen, K.M. (2004). The Flood Pulse Concept: New Aspects, Approaches,

Junk, W.J. (Ed.). (1997). *The Central Amazon Floodplain: Ecology of a Pulsing System*, Springer-

Pacific, Bangkok, Thailand, 2002, ISBN 978-0-12-088449-0

Verlag, New York, USA, ISBN 978-3540592761

Osteoglossomorpha): A reappraisal. *Journal of Zoology*, Vol.203, pp. 411-425, ISSN

development, In: *Human Ecology in Savanna Environments*, D.R. Harris (Ed.), 2-27,

Alto Camutins e a atual situação da Ilha do Pacoval, no Arari. *Instituto de* 

Dinâmica da Extração Madeireira no Estado do Pará, In: *Amazônia: Meio Ambiente e Desenvolvimento Agrícola*, A.K.O. Homma (Ed.), 161-186, EMBRAPA/SPI, Brasília,

de qualidade física de um solo de pastagem. *Pesquisa Agropecuária Brasileira*, Vol.35,

in the electric eel, *Electrophorus electricus*. *Zeitschrift für vergleichende Physiologie*,

and Applications – An Update. *Proceedings of the Second International Simposium on the Management of Large Rivers for Fisheries*. FAO Regional Office for Asia and the

(Eds.), 269-286, CRC Press, Texas, USA, ISBN-10: 084931514X

Cruz, M.E.M. (1987). *Marajó: Essa imensidão de ilha*, Parma, São Paulo, Brazil

Amazonia. *Biotropica*, Vol.10, pp. 170–183, ISSN 0006-3606

Academic Press, London, UK, ISBN 0-12-326550-9

*Antropologia e Etnologia do Pará*, Vol.5, pp. 5-32

Brazil, ISBN 8-57-383026-3

Vol.61, pp. 137-163

pp. 1493-1500, ISSN 1678-3921

Smithsonian Books, Washington D.C., USA, ISBN 1-588-34135-6

748–756, ISSN 0916-8451

No.3, pp. 319-328, ISSN 1679-6225

0006-8101

0952-8369

*Biology of sharks and their relatives*, J.C. Carrier, J.A. Musick and M.R. Heithaus M.R.

perspectives on seed consumption and dispersal by fishes. *BioScience*, Vol.57, pp.

Synbranchiformes: Synbranchidae) from ilha de Marajó, Pará, Brazil, with notes on its reproductive biology and larval development. *Neotropical Ichthyology*, Vol.3,


**13** 

*1Japan 2USA* 

*1Conservation International 2University of Wisconsin-Madison* 

**Biodiversity Conservation Planning in** 

**of Ecological and Visual Perspectives** 

Yoji Natori1, Janet Silbernagel2 and Michael S. Adams2

**Rural Landscapes in Japan: Integration** 

Conservationists worldwide have long been interested in rural landscapes (McNeely & Keeton, 1995; McNeely, 1995; Miller & Hobbs, 2002; Washitani, 2001; Yokohari et al., 2005), which can be characterized as semi-natural areas that are neither pristinely natural nor urban, maintained by appropriate level of human interventions. A great portion of the world's biodiversity is found in these landscapes (Pimentel et al., 1992). Such landscapes have gained an international attention as Satoyama, and an international partnership has been established in 2010 to promote sustainable use of human-influenced natural environment through the Satoyama Initiative (Convention on Biological Diversity Decision X/32). Japanese archipelago is one of the 34 Biodiversity Hotspots of the world (Mittermeier et al., 2004), and its biodiversity owe much to the quality of the human-influenced natural

Rural landscapes are an important conservation challenge in Japan because they are being lost rapidly. The challenge is that the traditional conservation strategy of "setting aside" will not work because humans play important roles in maintaining biodiversity on such landscapes (e.g., Farina, 1995; McNeely, 1995; Melnick, 1983; Nakagoshi, 1995; Natori et al., 2005; Washitani, 2001). Conservation in rural environments faces difficulties also because the public tends to associate nature conservation with pristine, untouched nature (Miller & Hobbs, 2002). The conservation of rural environments would require approaches different

Many have suggested that the consideration of the sociocultural dimension is crucial to the success of the conservation of rural environments in particular, and the conservation of biodiversity in general (e.g., Miller & Hobbs, 2002; Phillips, 1995; Pimentel et al., 1992; Saunders, 1990; Yokohari et al., 1994). Naveh (2000; 2001) has explicitly included humans in his theoretical development of a holistic approach to landscape studies. Born and Sonzogni (1995) and Margerum and Born (1995) have articulated a more pragmatic means to deal with environmental problems in the framework of integrated environmental management. Trauger (1999) calls for a shift from a traditional discipline-based approach to a problembased approach. Accordingly, transdisciplinary research is being advocated in recent years

from the traditional conservation strategies employed for pristine natural areas.

**1. Introduction** 

environment.

