Deforestation of the Brazilian Amazon
- Phillip FearnsidePhillip FearnsideInstituto Nacional de Pesquisas da Amazonia
Deforestation in Brazilian Amazonia destroys environmental services that are important for the whole world, and especially for Brazil itself. These services include maintaining biodiversity, avoiding global warming, and recycling water that provides rainfall to Amazonia, to other parts of Brazil, such as São Paulo, and to neighboring countries, such as Argentina. The forest also maintains the human populations and cultures that depend on it. Deforestation rates have gone up and down over the years with major economic cycles. A peak of 27,772 km2/year was reached in 2004, followed by a major decline to 4571 km2/year in 2012, after which the rate trended upward, reaching 7989 km2/year in 2016 (equivalent to about 1.5 hectares per minute). Most (70%) of the decline occurred by 2007, and the slowing in this period is almost entirely explained by declining prices of export commodities such as soy and beef. Government repression measures explain the continued decline from 2008 to 2012, but an important part of the effect of the repression program hinges on a fragile base: a 2008 decision that makes the absence of pending fines a prerequisite for obtaining credit for agriculture and ranching. This could be reversed at the stroke of a pen, and this is a priority for the powerful “ruralist” voting bloc in the National Congress. Massive plans for highways, dams, and other infrastructure in Amazonia, if carried out, will add to forces in the direction of increased deforestation.
Deforestation occurs for a wide variety of reasons that vary in different historical periods, in different locations, and in different phases of the process at any given location. Economic cycles, such as recessions and the ups and downs of commodity markets, are one influence. The traditional economic logic, where people deforest to make a profit by producing products from agriculture and ranching, is important but only a part of the story. Ulterior motives also drive deforestation. Land speculation is critical in many circumstances, where the increase in land values (bid up, for example, as a safe haven to protect money from hyperinflation) can yield much higher returns than anything produced by the land. Even without the hyperinflation that came under control in 1994, highway projects can yield speculative fortunes to those who are lucky or shrewd enough to have holdings along the highway route. The practical way to secure land holdings is to deforest for cattle pasture. This is also critical to obtaining and defending legal title to the land. In the past, it has also been the key to large ranches gaining generous fiscal incentives from the government. Money laundering also makes deforestation attractive, allowing funds from drug trafficking, tax evasion, and corruption to be converted to “legal” money. Deforestation receives impulses from logging, mining, and, especially, road construction. Soybeans and cattle ranching are the main replacements for forest, and recently expanded export markets are giving strength to these drivers. Population growth and household dynamics are important for areas dominated by small farmers. Extreme degradation, where tree mortality from logging and successive droughts and forest fires replace forest with open nonforest vegetation, is increasing as a kind of deforestation, and is likely to increase much more in the future.
Controlling deforestation requires addressing its multiple causes. Repression through fines and other command-and-control measures is essential to avoid a presumption of impunity, but these controls must be part of a broader program that addresses underlying causes. The many forms of government subsidies for deforestation must be removed or redirected, and the various ulterior motives must be combated. Industry agreements restricting commodity purchases from properties with illegal deforestation (or from areas cleared after a specified cutoff) have a place in efforts to contain forest loss, despite some problems. A “soy moratorium” has been in effect since 2006, and a “cattle agreement” since 2009. Creation and defense of protected areas is an important part of deforestation control, including both indigenous lands and a variety of kinds of “conservation units.” Containing infrastructure projects is essential if deforestation is to be held in check: once roads are built, much of what happens is outside the government’s control. The notion that the 2005–2012 deforestation slowdown means that the process is under control and that infrastructure projects can be built at will is extremely dangerous. One must also abandon myths that divert efforts to contain deforestation; these include “sustainable logging” and the use of “green” funds for expensive programs to reforest degraded lands rather than retain areas of remaining natural forests. Finally, one must provide alternatives to support the rural population of small farmers. Large investors, on the other hand, can fend for themselves. Tapping the value of the environmental services of the forest has been proposed as an alternative basis for sustaining both the rural population and the forest. Despite some progress, a variety of challenges remain. One thing is clear: most of Brazil’s Amazonian deforestation is not “development.” Trading the forest for a vast expanse of extensive cattle pasture does little to secure the well-being of the region’s rural population, is not sustainable, and sacrifices Amazonia’s most valuable resources.
What Is Deforestation?
“Deforestation” refers to converting forest into nonforest, and the meaning of the term therefore hinges on what is considered to be a “forest.” Semantic distinctions often confuse discussions of deforestation. In official Brazilian data, such as those from Project for Monitoring the Brazilian Amazon Forest by Satellite (PRODES), run by the National Institute for Space Research (Instituto Nacional de Pesquisas Espaciais [INPE]), deforestation refers to the clearing of primary or old-growth forest, not to the clearing of secondary forests. Secondary forests refer to succession in previously clear-cut areas (as distinct from the usage of this term in Southeast Asia to refer to logged forests). The PRODES surveys define forest-based on vegetation types classified by the Brazilian Institute of Geography and Statistics (Instituto Brasileiro de Geografia e Estatística, 2012), rather than by percentage cover (Instituto Nacional de Pesquisas Espaciais [INPE], 2013). The United Nations Framework Convention on Climate Change (UNFCCC), better known as the “Climate Convention,” defines “forest” as having at least 10% cover (Intergovernmental Panel on Climate Change, 2006, p. 4.74), allowing many types of cerrado (central Brazilian savanna) to be considered forest, and its clearing as “deforestation.” Note also that the Climate Convention definition, which is based on the definition used by the Food and Agriculture Organization of the United Nations (2012, p. 3), includes “temporarily unstocked” areas that have been completely clear-cut but are intended to be allowed to regenerate, thus opening a loophole by making the definition of forest, and therefore of deforestation, dependent on knowledge of intent rather than being based solely on objective measurements verifiable by satellite.
An important distinction is between net versus gross deforestation (e.g., Brown & Zarin, 2013). “Net” deforestation subtracts areas that are regenerating as secondary forests. Some interpretations also include silvicultural plantations, such as of Eucalyptus, as counting toward reducing net deforestation, including Brazil’s 2008 National Plan for Climate Change. This plan promised to end net deforestation by 2015 (Comitê Interministerial sobre Mudança do Clima, 2008, p. 12), an objective that was not met. A target of zero or reduced “net” deforestation carries a danger, as each hectare of plantation or regenerating trees effectively creates a license to clear a hectare of mature or primary forest elsewhere.
Brazil’s commitment part of the 2015 Paris accords refers to reaching zero “illegal” deforestation by 2030 (Republic of Brazil, 2015, p. 3). This far from means the end of deforestation, because forest clearing can continue as long it is “legal.” With advance of the Rural Environmental Register, all properties in the country should be registered long before 2030, making it easy to obtain permission for “legal” deforestation up to the limits specified by Brazil’s Forest Code (20% in Amazonia). But because in the early 21st century, many present and future properties in Amazon forest areas have little clearing, large amounts of “legal” deforestation can continue (Nunes, Gardner, Barlow, Martins, Salomão, & Souza, 2016).
Why Is Deforestation Important?
Brazil’s Amazonian deforestation is important to life throughout the world, both human and nonhuman. the impacts of deforestation include losses of environmental services that though they affect whole world, affect Brazil the most (e.g., Fearnside, 1997a, 2008a). The environmental services of Amazonian forest include its role in storing carbon and thus avoiding global warming (e.g., Fearnside, 2000, 2016a; Nogueira, Yanai, Fonseca, & Fearnside, 2015), in recycling water provides atmospheric water vapor that is important for rainfall not only in Amazonia but also in non-Amazonian areas such as São Paulo (e.g., Arraut, Nobre, Barbosa, Obregon, & Marengo, 2012), and in maintaining biodiversity (e.g., Fearnside, 1999). In addition, Amazonian forests provide a variety of material products, such as timber, rubber, and Brazil nuts; these provisioning functions currently support local populations and also represent lost opportunities for sustainable use when areas are deforested.
The vast size of Brazilian Amazonia (Figure 1) gives special importance to deforestation processes in this region. In many parts of the world that were originally covered by tropical forests, deforestation has proceeded to the point where only tiny remnants remain. In these areas, the clearing of the last hectares of remaining forest represents a tragedy for biodiversity. In Amazonia, despite the large area of remaining forest, deforestation has a significant impact on biodiversity because the distribution of species is not uniform. The ranges of many species have been restricted to parts of the region where forest has already been reduced to small fragments (e.g., Hubbell, He, Condit, Borda-de-Água, Kellnert, & ter Steege, 2008; Michalski & Peres, 2005). The disappearance of species that were endemic to heavily deforested areas in eastern and southern Amazonia is already widespread (e.g., Moura, Lees, Aleixo, Barlow, Dantas, Ferreira, et al., 2014).
The elimination of forest has different implications for biodiversity and for climate. Fighting to save the last remnants of forest in heavily deforested areas is essential for biodiversity, but from the point of view of climate, the dwindling area of remaining forest limits the potential impact of future deforestation. Although the impact on global warming is the same when a hectare of forest is cleared in any part of the world, assuming that forest biomass per hectare and other relevant parameters are the same, the equivalence is restricted to the emission from one year to the next. In the case of Amazonia, in addition to the yearly impact, the vast extent of remaining forest gives additional importance to deforestation processes because they can result in much greater future emissions. In countries where little forest remains, deforestation will diminish and end soon regardless of policy changes, any change in public policies in Brazil has a much greater potential impact, positive or negative, compared to other tropical countries. The various ways that Amazonian forest can be destroyed other than by deliberate human action give the region additional importance for global climate.
How Fast Has Deforestation Occurred?
Brazil’s Amazonian deforestation rates have varied widely the over the decades since construction on the Transamazon Highway (BR-230) began, in 1970, initiating the “modern” era of deforestation. Between 1978 (the year of images for the first LANDSAT satellite survey) and 1988 (the next complete survey), deforestation averaged 21,050 km2/year (Fearnside, 1990). Since then, annual coverage figures have been available, with the single exception of 1993 (INPE, 2017a). A long history of political interference with the monitoring program (Fearnside, 1997d) has largely been overcome, and the PRODES program currently has much greater transparency. Some discrepancies with other satellite estimates still remain open questions (Fearnside & Barbosa, 2004), whereas other LANDSAT estimates are highly consistent (Souza, Siqueira, Sales, Fonseca, Ribeiro, Numata, et al., 2013). Deforestation rates have undergone major oscillations (Figure 2), mostly as a result of macroeconomic shifts (Fearnside, 2005a).
PRODES uses Landsat-TM satellite imagery (or the equivalent) with 30-m resolution (INPE, 2017a). The imagery is freely available on the INPE website, degraded to 60-m resolution. Images are taken in the dry season (August in all but the extreme north of the region), and the “year” of the data refers approximately to the deforestation between August 1 of the previous year and July 31 of the nominal year. The lower limit for detection of clearings is 6.25 ha.
The INPE also has a program called DETER (Detection of Deforestation in Real Time), which produces monthly data from MODIS imagery with maximum resolution of 250 m (Diniz, Souza, Santos, Dias, da Luz, de Moraes et al., 2015; INPE, 2017b). This only detects clearings of 25 ha or larger. A similar MODIS-based monitoring program called SAD (Deforestation Alert Service) is run by the Institute for Man and the Environment in Amazonia (Instituto do Homem e Meio Ambiente da Amazônia [IMAZON]), a nongovernmental organization (NGO). The SAD data are released more quickly than the DETER data and are accompanied by more information on the deforestation processes in course (Instituto do Homem e Meio Ambiente da Amazônia, 2017). The results of the DETER program at INPE and the SAD program at IMAZON match well. Care is needed in drawing conclusions from the monthly data. These data are more readily affected by having significant areas covered by clouds than are PRODES data, despite the much more frequent satellite passes by MODIS compared to LANDSAT. More importantly, frequent headlines proclaiming that deforestation in a given month is several hundred percentage points higher or lower than in the same month in the previous year can often be misleading. If the month in question is in the dry season, this can be very significant, but if it is in the wet season, then large variation from a number near zero has little import, and the clearing detected is likely to be an insignificant portion of the annual total deforestation.
An important limitation of deforestation data is that forest degradation, such as by logging and by tree mortality from droughts and fire, is not detected or counted unless the forest has reached the extreme condition of being an open area with only a few scattered trees remaining, thus appearing as cleared on the satellite image. Extreme degradation of this type is counted as deforestation by all the programs mentionedin the preceding paragraph. There has been a long-standing struggle over this issue between the INPE and the state government of Mato Grosso, which insists that these areas are not “deforestation” areas because they were not deliberately clear-cut. This is likely to become even more critical if a proposed law (PL4508/2016) is implemented to allow “sustainable” cattle ranching in legal reserves (Canal Rural, 2017). Degradation is monitored by IMAZON (Cardoso, Ribeiro, Salomão, Fonseca, & Souza, 2017) and was monitored from 2007 to 2013 by the DEGRAD program at the INPE (INPE, 2014a).
Why Is Deforestation Happening?
Economic Cycles and Land Speculation
From 1988 to 1991 deforestation declined by half, during a time of a deepening economic recession under president Fernando Collor that culminated with the government ceasing deposits in bank accounts in 1990, meaning that funds were no longer available for investment in deforestation (among other effects). Deforestation rose in the subsequent years as the economy recovered, reaching a record rate of 29,100 km2/year in 1995, as a consequence of the June 1994 Real Plan, a package of economic reforms that ended hyperinflation. Money that had been invested in the “overnight” (a 24-hour money market that could protect money from inflation) was suddenly available, and it was invested in deforestation, and not, for example, in recuperating degraded pastureland. Deforestation fell dramatically during the next two years, another consequence of the Real Plan. Because the plan had essentially halted inflation, generalized land speculation became unprofitable (though land purchases in areas where roads would be built or upgraded could still yield quick fortunes). Even under the inflation regime that has prevailed since the 1994 Real Plan, with much lower rates than those before this plan, clearing behavior is also frequently explained by speculative returns instead of solely by beef production (Carrero & Fearnside, 2011; Razera, 2005).
Land speculation is an important force in deforestation because the practical way to secure land holdings is to deforest to create cattle pasture. Under hyperinflation, land values in Amazonia increased faster than the rates inflation, and the increase in land value could yield much more profit than could raising cattle or other activities undertaken while they are in possession (either legally or illegally) of the land (Hecht, 1985, 1993; Hecht, Norgaard, & Possio, 1988). Land values in Amazonia and deforestation rates both fell by half after the implementation of Real Plan, an indication of how strong speculation had been as a driver. However, land speculation continues to be an important component in the profitability of extensive ranching (Bowman, Soares-Filho, Merry, Nepstad, Rodrigues, & Almeida, 2012). Following the decline after the 1995 peak, deforestation rates increased to a new peak of 27,772 km2/year in 2004, thanks to a strengthening economy and rising commodity prices. Beginning in 2005, there was a major decline in deforestation rates until 2012, after which the rate increased (with oscillations), reaching 7989 km2/year in 2016 (INPE, 2017a).
Commodities and Governance
Understanding the causes of the 2005–2012 decline in deforestation rates is essential to the policy lessons that can be derived from this experience. The Brazilian government has repeatedly claimed that the decline was the result of government actions, particularly the increases in inspections and fines for those who deforest illegally. In fact, the decline was brought about by a variety of factors, including governance measures, and it is these other factors that explain most of the decline. The decline occurred in two phases, the first from 2005 to 2007, and the second from 2008 to 2012. During the period up to 2007, deforestation rates tracked the prices of export commodities, such as soybeans and beef, making these the primary drivers during this period (Assunção, Gandour, & Rocha, 2015; see also Arima, Barreto, Araujo, & Soares-Filho, 2014; Hargrave & Kis-Katos, 2013). For the 1995–2007 period, more than 75% of the deforestation is explained by lagged prices of soy and beef (Arima et al., 2014). Most (70%) of the total 2005–2012 decline had occurred by 2007. From 2008 onward, commodity prices recovered, though deforestation continued to decline to 2012, indicating that something had changed. An event in 2008 that coincides with the change is a resolution of the Brazilian Central Bank (BACEN 3545/2008), which blocks loans from government banks for agriculture and ranching in properties with fines pending in the environmental agencies (Börner, Kis-Katos, Hargrave & König, 2015; Fearnside, 2015e). The fines themselves have little effect, since they can be appealed almost indefinitely and are rarely paid (e.g., Lima, Capobianco, & Moutinho, 2009). In contrast, the block on loans has immediate effect and there is no chance of appeal; it also has its greatest impact on the largest actors. Another key event in 2008 was that the federal environmental agency, the Brazilian Institute for the Environment and Renewable Natural Resources (IBAMA) initiated a blacklist of municipalities with high deforestation. The blacklisted municipalities had a significantly greater reduction in deforestation as compared to non-blacklisted municipalities over the 2009–2011 period (Arima et al., 2014), a trend that continued through 2012 (Cisneros, Zhou, & Börner, 2015). Blacklisted municipalities had additional requirements for obtaining licenses for legal deforestation, had more inspection effort focused on them by IBAMA, suffered restrictions on agricultural credit, and had additional impetus to hasten implantation of the Rural Environmental Register due to increased assistance from NGOs in registering properties and because of local desire to avoid reputational costs (Cisneros et al., 2015).
The strength of governance measures varies with election cycles, and there is a tendency to relax enforcement of environmental regulations prior to major elections, producing a significant relation between deforestation rates and elections (Rodrigues-Filho, Verburg, Bursztyn, Lindoso, Debortoli, & Vilhena, 2015). The mere anticipation of such relaxation can stimulate clearing, as was suggested by a dramatic surge in deforestation in Mato Grosso, in 2002, in the months prior to election of Brazil’s largest soybean producer as governor of the state, thus curtailing the state government’s deforestation control program (e.g., Fearnside, 2005b).
In the 1970s and 1980s, fiscal incentives offered by the Brazilian government were a major factor motivating deforestation by large ranchers (Binswanger, 1991; Mahar, 1979). Incentives included the right to invest in approved Amazonian ranches funds that would otherwise have been paid as taxes on the profits of enterprises elsewhere in the country, generous loans at interest rates far below the rate of inflation, and tax exemptions on the Amazonian income. Clearing forest was primarily a means of gaining access to these subsidies, rather than of earning income from beef production. The effect of incentives continued long after official discourse stressed that the incentive program had been ended. A 1991 decree halted approvals of new projects, but the already approved projects continue to receive the tax incentives (Fearnside, 2005a). Natural attrition, such as by bankruptcy, has reduced the impact of the incentives by reducing the number of eligible ranches.
One of the most pervasive motives for deforestation is the establishment and maintenance of land tenure (Fearnside, 1979, 2001b). Much of the land in Brazilian Amazonia is in the public domain. Aside from occasional land distributions to small farmers in official settlement programs (such as those on the Transamazon Highway) and to large ranchers in areas that are sold through bidding (such as the Agriculture and Ranching District of the Manaus Free Trade Zone [SUFRAMA]), land enters the private domain by first being illegally invaded either by small squatters or by large grileiros (land thieves or “land grabbers”), and eventually the government recognizes the claims and grants title. The key to gaining title is showing “improvement” (benfeitoria) on the land, which means deforesting and planting something, cattle pasture being the cheapest option per hectare. But even if one has title to land, if it is left in forest, the owner can eventually expect to lose it, either through invasion by squatters or grileiros or by expropriation for a government settlement project.
The question of who is deforesting is essential to formulating policies that will be effective in containing the process. Deforestation is done for different reasons and by different actors in different parts of the region and in different historical periods in any given location. For example, land along the Belém-Brasília Highway (BR-010), built in the late 1950s and early 1960s, was first occupied by small squatters, who were later expelled (often violently) and replaced by large ranchers (Foweraker, 1981; Valverde & Dias, 1967). Similar patterns unfolded in much of southern Pará beginning in the 1970s (Schmink & Wood, 1992). The Transamazon Highway (BR-230), built in the early 1970s, was settled through government colonization projects in which small farmers received 100-ha lots (e.g., Moran, 1981; Smith, 1982). Many of these lots were later acquired by wealthier actors, who then proceed to use them as medium to large ranches (e.g., Fearnside, 1986b). A similar process took place along the Cuiabá-Porto Velho (BR-364) Highway in Rondônia (Fearnside, 1984). In Amazonia as a whole, large (officially defined in Brazilian Amazonia as > 1000 ha) and medium-sized (101–1000 ha) actors have traditionally predominated in deforestation (Fearnside, 1993, 2008b); but the relative importance of small (≤ 100 ha) farmers has been increasing, as indicated by the decreasing average size of new clearings (Rosa, Souza, & Ewers, 2012), and the deforestation slowdown since 2005 has disproportionately affected the larger actors (Godar, Gardner, Tizado, & Pacheco, 2014). However, small farmers have demonstrated greater potential to stabilize their land use in a mosaic of agriculture, pasture, and natural forest, and avoiding the consolidation of small properties into large ranches represents a beneficial measure from the point of view of minimizing deforestation (Campos & Nepstad, 2006; Godar, Tizado, & Pokorny, 2012).
Money from such sources as drug trafficking, truck hijacking, government corruption, and income sources not declared to tax authorities can be invested in Amazonian deforestation with minimal risk. If the same funds were invested in the stock market or urban real estate, the inconsistency in declared income would soon be discovered by tax authorities. Illegal money forms a sort of cloud over Amazonia that affects what happens on the ground, often defying traditional economic logic. The terra do meio, an area in Pará the size of Switzerland, has for many years been essentially outside of the control of the Brazilian government (Greenpeace, 2003; Taravella, 2008). The area has been dominated by drug traffickers, grileiros, and other illegal actors (Escada, Vieira, Amaral, Araújo, da Veiga, Aguiar et al., 2005; Fearnside, 2008b; Greenpeace, 2003; Instituto Socioambiental, 2016; Schönenberg, 2002). In 2005, following the assassination of Dorothy Stang (a defender of Amazonian social and environmental causes), a group contiguous of protected areas (known in Brazil as a “mosaic”) was created in the terra do meio, but the environmental agencies have yet to establish a physical base in the area, something that has been planned since 2002. An example of deforestation that is inexplicable by traditional economic logic is provided by a 6239-ha clearing (known as the “revolver” because of its shape) that suddenly appeared, in 2003, in the terra do meio (Venturieri, Aguiar, Monteiro, Carneiro, Alves, Câmara et al., 2004). The location was far from any roads and had been classified as one of the least-promising locations for profitable ranching in all of Amazonia, based on the calculated farm-gate price of beef (Arima, Barreto, & Brito, 2005, p. 50).
Logging is an important driver of deforestation, though its effect is delayed and hard to show statistically because in areas with active logging there is little deforestation, whereas in those where deforestation is in full swing, timber is no longer available for logging. Logging facilitates deforestation by providing clandestine “endogenous” roads that are subsequently used for entry of deforesters (Arima, Walker, Perz, & Caldas, 2005). It also provides much of the money that pays for the felling itself, in the cases of both large actors and small ones (Veríssimo, Uhl, Mattos, Brandino, & Vieira, 2002).
Mining is another driver of deforestation. Gold miners (garimpeiros), who are attracted to areas with alluvial deposits, can stay on later as squatters or invest proceeds in land or in clearing (MacMillan, 1995). Iron mining in the Carajás area justified a major government program to promote agriculture and ranching in the region and also feeds pig-iron smelters who draw wood from the surrounding region for charcoal (Fearnside, 1986a, 1989a). Bauxite mining, aside from the mine sites themselves, feeds an aluminum smelting industry that drives massive impacts from the hydroelectric dams that are built to supply the smelters (Fearnside, 2016d). The areas surrounding dams are associated with increased deforestation (Barreto, Brandão, Martins, Silva, Souza, Sales et al., 2011; Baretto, Brandão, Silva, & Souza, 2014; Fearnside, 2014a, 2014b).
Roads are the most powerful driver of deforestation (Kirby, Laurance, Albernaz, Schroth, Fearnside, Bergen et al., 2006; Laurance, Cochrane, Bergen, Fearnside, Delamônica, Barber et al., 2001; Pfaff, 1999; Pfaff, Robalino, Walker, Aldrich, Reis, Perz et al., 2007; Soares-Filho, Nepstad, Curran, Cerqueira, Garcia, Ramos et al., 2006). The construction or upgrading of a road increases migration to the area it accesses; increases the profitability of agriculture and ranching; and greatly increases land values, with consequent speculative deforestation and a turnover of landowners in favor of wealthier actors who deforest faster than the previous owners (Fearnside, 1987a, 1987b). Deforestation follows roads, and the presence of deforestation has a contagious effect, leading to further acceleration of deforestation along these routes (Rosa, Purves, Carreiras, & Ewers, 2014; Rosa, Purves, Souza, & Ewers, 2013). Roughly 80% of the forest loss in Brazilian Amazonia has been in the “arc of deforestation,” a crescent-shaped strip along the southern and eastern edges of the forest (Figure 3). New highways are bringing deforestation activity into the heart of the Amazon. The most critical case is the planned reconstruction of the abandoned Manaus-Porto Velho (BR-319) Highway, which would connect the arc of deforestation with central Amazonia, bringing the actors and processes from Rondônia to large areas in Amazonas and Roraima that have road access from Manaus, and open the large block of intact forest in the western portion of the state of Amazonas through planned side roads (Fearnside & Graça, 2006). The environmental impact statement for this planned highway presented Yellowstone National Park as the expected deforestation scenario, envisioning tourists driving through the area on a “park-highway” without cutting a single tree (see Fearnside, 2015d; Fearnside & Graça, 2009). The unreality of this portrayal of an Amazon frontier would be hard to exaggerate. Unrealistic “governance scenarios” like this are simply excuses that serve to justify the licensing of highways, which imply very real impacts.
Soybeans have been a major force behind deforestation in Mato Grosso, and there have also been advances in some parts of Pará, particularly the Santarém area (Barona, Ramankutty, Hyman, & Coomes, 2010; Fearnside, 2001c; Morton, DeFries, Shimabukuro, Anderson, Arai, del Bon Espirito-Santo et al., 2006). Besides the direct conversion of forest for soy, the crop has a very important indirect impact. Soy advance into pasture in the cerrado (as well as into forest areas in northern Mato Grosso) has a prominent role in driving increased investment in clearing for ranches in Amazon rainforest areas in Pará (Arima, Richards, Walker, & Caldas, 2011; Richards, Walker, & Arima, 2014). The Chinese have played a key role in driving the conversion of forest and cerrado (Fearnside, Figueiredo, & Bonjour, 2013). This has primarily been through exports, but it has also been through land purchases and the financing of transport infrastructure. Transport infrastructure is the main limitation on the spread of soybeans from the most profitable areas in Mato Grosso, particularly to the west in Rondônia and Acre, as well as in the portions of northern Mato Grosso still dominated by pasture (Vera-Diaz, Kaufmann, Nepstad, & Schlesinger, 2008).
International finance has played a significant role in speeding the advance of soy. In 2002 and 2003 the International Finance Corporation (IFC), the arm of the World Bank that finances private companies, granted Grupo André Maggi (Brazil’s largest soy company) two US$30 million loans. The IFC classified the loans as Category B (low environmental risk), thus not requiring any environmental-impact assessment or subsequent monitoring of impacts. This IFC classification allowed Rabobank (of the Netherlands) to grant Maggi two loans totaling US$330 million (Greenpeace, 2006, p. 18). Financing from the Brazilian government’s National Bank for Social and Economic Development (BNDES) has also been a major force in the advance of soy (Greenpeace, 2006).
It should be noted that gross domestic product (GDP) is not a good predictor of deforestation. Statements associating GDP with clearing give the false impression that deforestation is an inevitable consequence of economic progress. The fraction of Brazil’s economy contributed by new clearing on the Amazon frontier is minimal, although the large areas of soybeans in previously cleared areas are a significant contributor. The questionable nature of a link to GDP is shown by “decoupling” of deforestation rates from agricultural production during the 2005–2012 deforestation slowdown (Lapola, Martinelli, Peres, Ometto, Ferreira, Nobre et al., 2014; Nepstad, Irawau, Bezerra, Boyd, Stickler, Shimada et al., 2013; Nepstad, McGrath, Stickler, Alencar, Azevedo, Swette et al., 2014).
Cattle production (as opposed to ulterior motives) is becoming more prominent in the mix of deforestation motives in Amazonia. This is behavior that following the traditional economic logic, in which actors deforest to earn profits from the sale of products from agriculture and ranching (Faminow, 1998; Margulis, 2004; Mattos & Uhl, 1994; Mertens, Poccard-Chapuis, Piketty, Laques, & Venturieri, 2002). Forest conservation ultimately requires addressing the “underpinnings of the cattle economy itself” (Walker, Moran, & Anselin, 2000). Cattle ranching is even accelerating in the extractive reserves, created to maintain forests by supporting traditional populations of rubber tappers and Brazil-nut gatherers; ranching has proliferated in these areas and is replacing the economy based on nontimber forest products (Salisbury & Schmink, 2007). Rubber extraction is not economically viable without subsidies (Jaramillo-Giraldo, Soares Filho, Ribeiro, & Gonçalves, 2017).
Export in general has become a more prominent predictor of deforestation at the municipality (county) level (Faria & Almeida, 2016). The increase in beef exports is especially significant because of the great potential for expansion (McAlpine, Etter, Fearnside, Seabrook, & Laurance, 2009). Brazilian exports of frozen beef were barred from virtually all international markets because of the presence of foot-and-mouth disease (Fearnside, 1987a). Brazilian Amazonia was thereby protected from the “hamburger connection” (Myers, 1981) that has driven much of the deforestation in Central America, an area that is free of the disease. Beginning in 1998, states in Brazil were successively certified as free of foot-and-mouth disease, starting with the non-Amazonian states in the south (Kaimowitz, Mertens, Wunder, & Pacheco, 2004). This had an indirect impact on Amazonia in that beef produced in southern Brazil could be exported; whereas people in São Paulo, for example, could eat beef from Pará. All nine states in Brazilian Amazonia have, since 2015, been classified as having, at most, a medium risk, in addition to being without clinical cases of the disease; but Amazonas, Roraima, and Amapá have not been classified as “disease free,” which would allow direct exports from these states (Pithan e Silva, 2016). Brazil is the world’s largest exporter of beef, some of which is even exported as live cattle. In 2015 and 2016, accords with Russia, the United States, and China opened these markets to Brazilian beef. The full opening of the Chinese market is particularly significant, since its potential scale is essentially infinite from the perspective of Brazilian producers. In addition to dominating beef exports to China, Brazil is also China’s main supplier of leather. China is the world’s largest manufacturer of shoes. In 2008, the value of Brazil’s leather exports totaled US$1.9 billion, as compared to US$5.1 billion for beef (Greenpeace, 2009, p. 61).
The Brazilian government’s generous subsidies for ranching in the 1970s and 1980s came during the “economic miracle” period, and their later curtailment was coincident with a severe recession. As in the case of soybeans, international finance has contributed to speeding up of the current “modern” period of livestock production and processing. In March 2007, the IFC made a US$90 million loan to Bertin (Brazil’s largest slaughterhouse company at the time), which supplied beef to Burger King, among many other outlets (Greenpeace, 2009; Rich, 2013). Brazilian government financing from BNDES has also been important in advancing the modern livestock industry in Amazonia.
Increasing population has a significant effect on Brazil’s Amazonian deforestation (Laurance, Albernaz, Schroth, Fearnside, Bergen, Venticinque et al,, 2002). However, interpreting the relationship is more complicated than might be thought. Studies that look at political units, such as countries, states, or municipalities, or at arbitrary geographic units, such as grid cells, will find results on population change and deforestation rate that go in both directions and will conclude that there is no relationship between these two variables. The first step to make sense of such data is removing the urban population from the analysis. While the urban population has an effect, it is very distinct from the effect of the direct deforestation actors. Then, there must be a breakdown by the different rural actors who are present before and after the land-use transformation under study, such as deforestation in a given period. These data do not exist for Brazil. The only solution is to obtain detailed information from case studies in specific locations. It is important that the locations chosen be “typical” of large areas of deforestation. The places being converted to cattle pastures in Brazilian Amazonia represent an obvious priority.
Two key questions affecting the relationship of population and deforestation are (a) who are the actors, such as ranchers versus small farmers, and (b) what population and land use is being replaced. If the situation is one of small farmers replacing “unoccupied” forest, then a greater population (of small farmers) translates into more deforestation. If it is ranchers who are replacing “unoccupied” forest, then the same relationship applies, although the number of people will be lower and the amount of deforestation per capita will be much greater. If the situation is one of ranchers replacing small farmers, then the human population will decrease and the rate of deforestation per capita will increase, resulting in a negative relationship between population change and deforestation rate.
One theory regarding population is that increasing rural-urban migration will result in the abandonment of large areas that are currently used for agriculture and ranching, leading to the establishment of secondary forests and a recovery of biodiversity (Wright & Muller-Landau, 2006). Unfortunately, other than existence of significant rural-urban migration (Parry, Day, Amaral, & Peres, 2010), this theory bears little resemblance to events in Amazonia (Fearnside, 2008c). Those who migrate to cities are usually riverside inhabitants, who do very little deforestation. Were larger actors to give up their operations and move to cities, their land would be sold to others who would continue to use the cleared areas (sometimes with intervals under secondary succession). Cattle pasture requires very little labor once established, and a small population can occupy a very large area.
Household processes among small farmers can result in deforestation that is independent of the profit-seeking motive, which can be used as a lever by incentive programs to change clearing behavior. These include household demographic changes and the economic circumstances of each family (Caldas, Walker, Arima, Perz, Aldrich, & Simmons, 2007). At the stage in the household life cycle when both labor capability and the demand for consumption to support dependents are at a maximum, deforestation advances at maximum speed and is unlikely to be influenced by outside policy interventions. Minimizing risks takes precedence over maximizing profits (Walker, Perz, Caldas, & Silva, 2002).
Forest can be converted to nonforest (i.e., deforested) by extreme degradation rather than by clear-cutting. Degradation is becoming increasingly prevalent in Brazilian Amazonia and has not been affected by the forces that shifted deforestation rates to a lower plateau after 2004 (Souza et al., 2013). Logging is a major factor that even prior to the deforestation “slowdown” affected a larger area each year than the annual clear-cut (Asner, Knapp, Broadbent, Oliveira, Keller, & Silva, 2005). Logging has increased since the slowdown began, rather than decreasing in parallel with the deforestation (e.g., Silvestrini, Soares-Filho, Nepstad, Coe, Rodrigues, & Assunção, 2011), making the post-slowdown area that is subjected to logging each year far greater than the area that is deforested outright. Logging makes forests more susceptible to entry of fire because it leaves slash and unintentionally killed trees in the forest that can act as fuel, and also opens canopy gaps that allow sunlight and wind to enter, hastening the drying of the fuel bed (Cochrane, Alencar, Schulze, Souza, Nepstad, Lefebvre et al., 1999; Nepstad, Verissimo, Alencar, Nobre, Lima, Lefebvre et al., 1999; Uhl & Buschbacher, 1985). This sets in motion a positive-feedback process that successively degrades the forest by the repeated entry of fire (Barlow & Peres, 2006; Nepstad, Carvalho, Barros, Alencar, Capobianco, Bishop et al., 2001). Droughts are major factors in facilitating Amazonian forest fires, with or without logging (Alencar, Nepstad, & Diaz, 2006; Aragão & Shimabukuro, 2010; Barbosa & Fearnside, 1999; Barlow & Peres, 2008; Barlow, Peres, Lagan, & Haugaasen, 2003; Berenguer, Ferreira, Gardner, Aragão, de Camargo, Cerri et al., 2014; Vasconcelos, Fearnside, Graça, Nogueira, de Oliveira, & Figueiredo, 2013). Droughts also degrade forest by killing trees for lack of water, even in the absence of fire (Lewis et al., 2011; Nepstad, Tohver, Ray, Moutinho, & Cardinot, 2007; Phillips, Aragão, Fisher, Lloyd, Lopez-Gonzalez et al., 2009). Severe droughts are becoming more frequent in Amazonia, for various reasons (Marengo & Espinoza, 2016), and climate-change projections indicate the likelihood of substantial future increases in these events (e.g., Malhi, Roberts, Betts, Killeen, Li, & Nobre, 2008). Loss of biodiversity caused by anthropogenic disturbances may even double the losses caused by the deforestation itself, as shown by study in Pará that found median losses from perturbation to be larger than those from deforestation in three of the five areas of endemism in this state (Barlow, Lennox, Ferreira, Berenguer, Lees, MacNally et al., 2016). In addition to degradation from logging and fire, hunting threatens wildlife (Antunes, Fewster, Venticinque, Peres, Levi, Rohe et al., 2016) and removes animals essential for the reproduction and dispersal of trees (Peres, Emilio, Schietti, Desmoulière, & Levi, 2016).
The Post-slowdown Deforestation Surge
Following the 27,772-km2/year peak of deforestation in 2004, rates fell by 84% to 4571 km2/year in 2012. This engendered a dangerous illusion in Brasília that deforestation was under control and that the government could therefore build roads, dams, and other infrastructure without putting the forest at risk. Unfortunately, this was never the case. Deforestation rates have trended upward since 2012, and jumped by 29% in 2016. The underlying forces behind deforestation have increased each year, with ever more population, investment, and roads that give deforesters access to the forest. More international markets were opening for Brazilian beef during this period, and exports were expanding. The reversal of the deforestation decline in 2012 coincided with the enactment of a major weakening of Brazil’s Forest Code, reducing restrictions on clearing near rivers and on steep hillsides and pardoning vast areas of illegal clearing done by 2008, with significant environmental and social consequences (Metzger, Lewinsohn, Joly, Verdade, & Rodrigues, 2010; Soares-Filho, Rajão, Macedo, Carneiro, Costa, Coe et al., 2014). Most importantly, this demonstrated the extraordinary influence of the “ruralist” bloc (representatives of large landholders) and created an anticipation of future “amnesties.”
The 1965 Forest Code (Law 4771/1965), a package of regulations governing deforestation, was replaced by Law 12,651/2012. In 2011, the initial vote in the House of Deputies, where representation is proportional to population, approved the revision by a ratio of 7:1. Since 85% of Brazil’s population is urban, the vast majority of the electorate has no financial stake in being allowed to deforest more, especially in risk-prone locations. Opinion polls showed 80% of Brazil’s population opposing any changes in the Forest Code (Lopes, 2011). The power of money from soy and other agribusiness interests is believed to be the most logical explanation for the outcome (Fearnside & Figueiredo, 2016).
The most noteworthy at the time of the deforestation surge in 2016 was the political uncertainty during and after the trial of president Dilma Rousseff, who was forced to step aside when her trial began in March 2016, culminating in her formal impeachment in August 2016. The uncertainty in 2016 offered an opportunity for the rapid advancement of legislative initiatives to remove environmental restrictions, and this continued following the formal transfer of presidential powers (Fearnside, 2016b). Other factors may have contributed. The value of the Brazilian real relative to the US dollar decreased by 12% from January to May 2016 (the period when decisions regarding deforestation are usually made), increasing the attractiveness of exporting soy and beef. Beef prices rose by 5%, and soy prices rose by 12.5%. The May 2016 soy price was 18% above the May average for the preceding five years. These economic factors would have contributed to the 2016 surge, but the magnitude of the surge suggests that it also had roots in the spectacular rise in the political power of the ruralists, which had begun well before the end of the previous presidential administration (Fearnside, 2017d).
The similarities and differences in the changes in deforestation rates among the nine states in Legal Amazonia are revealing. Deforestation rates increased in all states except Amapá and Mato Grosso. Amapá is insignificant, since the state only accounted for 0.3% of the total deforestation in 2016. Deforestation in Mato Grosso in 2016 was 1508 km2, though this was 5.8% less than in the preceding year. Mato Grosso has a substantial influence from soybeans, whereas in the other states the vast majority of clearing is for pasture. The importance of Mato Grosso relative to other Amazonian states has been decreasing, from 43.1% of the total deforestation in 2004 to 18.9% in 2016, reflecting the dwindling areas of remaining forest in places that are topographically favorable for mechanized agriculture. Other factors leading to decreased clearing in Mato Grosso include the predominance of large properties in this state; these properties are more sensitive to repression measures than are smaller ones (Godar et al., 2014). The distribution of the 2016 surge among Amazonian states suggests a continuation of trends to increased prominence of ranching relative to direct deforestation for soybeans, and of greater importance of smaller properties relative to larger ones.
How Can Deforestation Be Controlled?
Inspection and the punishment of illegal deforestation is an important part of any effort to control the process, because the lack of this form of action fosters an assumption of impunity, with far-reaching consequences. Monitoring capabilities are important to these efforts, and the advent of the DETER program, in 2004, provided an essential tool to allow reaction within a meaningful time period (Assunção, Gandour, & Rocha, 2013). Since 2003, Brazil’s command-and-control program is administered under the Plan of Action for Prevention and Control of Deforestation in Legal Amazonia (PPCDAm) (Ministério do Meio Ambiente, 2013). The program has had measurable effects (Arima et al., 2014).
Amazonian deforestation can be controlled, but the unfounded notion that it is under control and that therefore new roads, dams, and other infrastructure projects can be built without increasing deforestation is very dangerous. The official government interpretation—that the 2005–2012 decline proves that deforestation is under control—has been repeated countless times. However, falling commodity prices (rather than governance measures) account for nearly all the decrease in deforestation rates between 2005 and 2007, which represents 70% of the total through 2012, when the downward trend ended. Deforestation rates did not continue to decline after 2012, despite frequent official statements implying that the decline continued.
The effect of the repression program since 2008 rests on a fragile foundation: the 2008 Central Bank resolution linking government bank loans to an absence of pending fines (Fearnside, 2015e). This is because the ruralist bloc has enormous influence in the national legislature, and revoking the Central Bank resolution is one of its priorities. The effectiveness of the repression program could literally be removed at the stroke of a pen.
An example of the potential for the repression of deforestation to have an effect on clearing rates is provided by a state government program, from 1999 to 2001, in Mato Grosso (Fearnside, 2003b). At a time when deforestation was increasing in Amazonia as a whole, the trends in Mato Grosso turned from increases to decreases in municipalities in which significant amounts forest were still available for clearing (deforestation will tend to zero independent of any repression program in municipalities with little left to clear). However, after the election of Brazil’s largest soy entrepreneur as governor, in 2002, the program was gutted and entered a phase of “institutional subversion” (Rajão, Azevedo, & Stabile, 2012).
It is important that direct deforestation control measures, such as fining property owners who clear without the required licensing and restricting credit in municipalities (counties) that have been blacklisted for illegal deforestation, can have a significant effect (Tasker & Arima, 2016). The Brazilian foreign ministry’s long opposition to any form of international payment for avoiding deforestation was based on the belief of key individuals that controlling deforestation was impossible (Fearnside, 2012a). Indeed, the succession of “packages” of control measures implemented after each rise in clearing rates seemed to have no effect. Brazil changed its position in 2007, after the “slowdown” in deforestation was well underway.
Remove or Redirect Subsidies
Subsides take many forms besides the notorious fiscal incentives that massively subsidized large cattle ranches in the 1970s and 1980s. Low-interest loans are provided for actors of various sizes, including small farmers. A large subsidy, which often goes unrecognized, results from periodic “amnesties,” forgiving debts for farmers, both large and small, whose crops have failed because of weather events or other general misfortunes, thus transferring the risk of these agricultural activities to the taxpayers (e.g., Fearnside, 2001b). Of course, a wide array of other government expenditures provides transport infrastructure and other services in remote locations, generally with only a minimal return to the government in the form of taxes. In the case of small farmers, the fact that a substantial fraction of the economically disadvantaged portions of Brazil’s rural population depends on government bolsas (stipends), such as the family stipend (bolsa família), and on rural retirement benefits for elderly family members, represents a substantial subsidy that maintains families in agricultural activities even when they are unprofitable in their own right. Although they are closely tied to electoral politics, these income-redistribution programs are based on poverty-reduction objectives that apply to both rural and urban residents throughout the country as a matter of social justice. Government stipends maintain important deforestation actors, such as sem terras (organized landless workers). These actors have a key role in settlement establishment and deforestation (Simmons, Walker, Perz, Aldrich, Caldas, Pereira et al., 2010). Government settlement projects are heavily subsidized (Peres & Schneider, 2012). Even at the low levels of deforestation by small farmers, rural residents emit far more greenhouse gases than do urban residents, and the impact of the larger actors is very much greater (Fearnside, 2001a). Preventing rural-urban migration is seen as socially desirable, both by rural people who want to stay where they are and by urban residents who fear the social impact of burgeoning cities. However, municipality-level data in Amazonia indicate a positive effect of urbanization on well-being as measured by the human development index (HDI) (Caviglia-Harris, Sills, Bell, Harris, Mullan, & Roberts, 2016). The questions of how much rural subsidy is appropriate and of what types are extremely delicate ones.
Remove Ulterior Motives
Land speculation is a motive for deforestation that has essentially no benefit for the country and leads to substantial environmental damage. It needs to be stopped by government actions such as taxes and fines.
The present system of land-tenure establishment, which is based on deforestation, must end. Brazil has yet to make the transition from the centuries-old custom of the “regularization” of de facto possession of illegal land claims to one in which the population assumes as a matter of course that illegal occupation of land will not eventually result in a land title. A significant setback occurred in 2009, with Provisional Measure (MP) 158 (Law No. 11,952) creating the terra legal (legal land) program that legalizes claims up to 1500 ha (which can hardly be considered a small farm). Large illegal claims are often subdivided among the various members of an extended family to gain legal title within the limits of the program. The amount of land potentially to be legalized totals 67 million ha, or half the size of the state of Pará (Fearnside, 2013a). Most pernicious, the program leads to the logical assumption by present and future grileiros and squatters throughout the region that their claims will eventually be legalized by subsequent regularization programs. Achieving the goal of Amazonia becoming a landscape with defined and secure land tenure is essential for many reasons, including encouraging more sustainable behavior by landholders and assuring the rights of exclusion that must underlie any program for payment for environmental services, but a path to reaching this goal without provoking the perverse assumption of an eternally moving “line in the sand” has yet to be found. The “closing of the frontier” in 1890 in the western United States (Turner, 1893) has yet to have its parallel in Brazilian Amazonia, and a way must be found to achieve this by means other than simply running out of land (Fearnside & Graça, 2006).
Land-tenure establishment is handled by the National Institute for Colonization and Agrarian Reform (INCRA), which in recent years has acted almost entirely reactively, resettling squatters and sem terras (members of organized landless movements) in official settlement areas (Fearnside, 2001b). Settlements represented 13.5% of all deforestation up to 2011 in the 1911 settlements included in a study by Schneider and Peres (2015). In a study by Yanai, Nogueira, Graça, and Fearnside (2017) covering 3325 settlements, the settlements accounted for of 21% of the deforestation up to 2013. This process has no natural stopping point because the number of landless farmers in the country exceeds the capacity of the entire Amazon region if distributed in settlement areas (Fearnside, 1985). Caldas, Simmons, Walker, Perz, Aldrich, Pereira et al. (2010) expressed the implications most eloquently, “It is time to recognize past mistakes and adapt the land policy to the new reality in the Amazon that takes into consideration the environmental problems that current laws are causing. If we do not act now, the future of the poor in the region will not change; and the same cyclic processes of land occupation and degradation will occur until no forest will remain to support life in the region.”
On July 24, 2006, three months after the release of the Greenpeace (2006) report “Eating Up the Amazon,” Cargill and other major soy exporters of were convinced to sign a “soy moratorium” that committed them to not buy soy grown in the Amazon on land deforested after 2006 (a cutoff that was relaxed to 2008 in 2013). The moratorium was successively renewed, and in 2016 it was made permanent. It has had a measurable effect in reducing new forest clearing for soy (Adario, 2016; Gibbs, Rausch, Munger, Schelly, Morton, Noojipady et al., 2015). However, the soy moratorium cannot be credited with the overall decline in deforestation rates in Amazonia (the “slowdown”), as has sometimes been implied. The departure of overall deforestation rates from what is explained by commodity prices only began in 2008, not in 2006. The direct conversions affected by the moratorium are only a portion of the impact of soy. The moratorium does not include the cerrado, where soy expansion continues unfettered. The displaced deforestation from pastures converted to soy (either in the cerrado or in the Amazon forest) causes increasing clearing of Amazon forest for pasture, not only by means of the invisible hand of the economy, as ranchers respond to price signals, but also directly by the migration of ranchers themselves to rainforest areas. When an area becomes more profitable to use as soy than as pasture, as happened, for example, in Mato Grosso, ranchers do not switch to become soy planters. Instead, the ranchers (who represent a distinct cultural group in Amazonia; see Hoelle, 2015) will sell their land to a buyer with a soy-planting background (often arriving from non-Amazonian states such as Rio Grande do Sul), and the rancher will use the proceeds of the sale to buy a much larger area of cheap land in Pará on which to establish a new ranch.
Another limitation is that significant markets exist outside the exporting companies that participate in the soy moratorium. Since 2013 the main destination for Brazilian soy has been China, where purchases are little influenced by environmental impacts in other parts of the world. There are also domestic markets, including the market for soy oil in Brazil’s biodiesel program (Fearnside, 2009b).
In June 2009 Greenpeace released a report entitled “Slaughtering the Amazon” (Greenpeace, 2009), and four months later, the “cattle agreement” was signed by major slaughterhouses: JBS (Friboi), Bertin, Minerva, and Marfrig. There were actually two agreements: in July 2009, a term of adjustment of conduct was signed; and in October 2009, a zero deforestation agreement (G4). The agreements have been found to have had an effect in reducing deforestation despite problems with “laundering” cattle (Gibbs, Munger, L’Roe, Barreto, Pereira, Christie et al., 2016). “Laundering” cattle occurs when a nonparticipating ranch moves its cattle to a participating ranch, from which the cattle are sold to one of the signatory slaughterhouses. Improbably high cattle production per hectare of pasture is a sign that ranches are acting as intermediaries. This is a “common and accepted practice” and is not prohibited by the cattle agreement (Gibbs et al., 2016, p. 8). The monitoring system tracks only properties, not individual cows (which would need to be identified by ear tags, for example). The cattle agreement is most relevant for beef being exported to other countries, although the adherence of Brazil’s largest supermarket chain (Pão de Açucar) in 2016 is an important milestone in the domestic market (Charoux, 2016). Earlier, 35 Brazilian supermarket chains had discontinued beef purchases from offending slaughterhouses, and similar commitments had been made by some leather buyers (Arima et al., 2014, p. 467). As with soybeans, the fact that China is the major destination for beef undermines any possibility of pressure from consumers there affecting adherence.
An example of the problems with the cattle agreement is provided by JBS (which gets its name from the initials of its founder, João Batista Sobrinho), which, including the fusion of Friboi and Bertin, which it acquired on October 27, 2009, is the world’s largest processer of cattle products. Shortly before the cattle agreement, Greenpeace reported a large number of cattle purchases by Bertin from ranches that had been embargoed (Greenpeace, 2009). After the cattle agreement, the federal prosecutor’s office found a similar pattern of violation by JBS (Greenpeace, 2011); in 2012, JBS recommitted to the cattle agreement.
Creating and defending protected areas is an important component of any strategy for containing deforestation. Protected areas in Brazil include both indigenous lands, which are under the National Foundation of the Indian (FUNAI), and “conservation units,” which are under the Ministry of the Environment (Ministério do Meio Ambiente [MMA]) if federal, or under equivalent state-level agencies if created by the state governments. Since advent of the National System of Conservation Units (SNUC), in 2000, conservation units are classified into categories as “integral protection” and “sustainable use” (Ministério do Meio Ambiente, 2015). The integral protection category is for various kinds of parks and reserves that exclude human residents; the sustainable use category includes forests for timber management, “extractive reserves” for rubber tappers and other collectors of nontimber forest products, and “sustainable development reserves” with riverside dwellers and other traditional residents. Overlap sometimes occurs between indigenous territories and conservation units, leading to conflicts among government agencies and between the resident populations and the agencies. A case in point is a national forest (for timber management) that was created on the Tapajós River without considering the needs of the Munduruku indigenous residents, who are struggling to have the area declared as an indigenous land (Fearnside, 2015b).
Protected areas have a significant effect on preventing deforestation (Ferreira, Venticinque, & de Almeida, 2005; Ricketts, Soares-Filho, da Fonseca, Nepstad, Petsonk, Anderson et al., 2010; Veríssimo, Rolla, Vedoveto, & Futada, 2011; Walker, Moore, Arima, Perz, Simmons, Caldas et al., 2009). Location with respect to the arc of deforestation is important in this effect (Nolte, Agrawal, Silvius, & Soares-Filho, 2013), and the defensibility of the sites chosen should be an essential criterion in selecting areas (Peres & Terborgh, 1995). The category of the protected area, together with its administration at the state or federal level, affects reserve effectiveness in preventing deforestation (Vitel, Fearnside, & Graça, 2009). Locational effects and political pressures can obscure these differences (Pfaff, Robalino, Sandoval, & Herrera, 2015). Indigenous lands have the best record in excluding deforestation (Nepstad, Schwartzman, Bamberger, Santilli, Ray, Schlesinger et al., 2006). In the case of the Amazon Protected Areas Program (ARPA), which beginning in 2002 created and fortified a series of conservation units to meet an objective of protecting 600,000 km2of Amazonian forest, the reserves have been shown to imply a reduction in deforestation (Nepstad et al., 2006; Soares-Filho, Moutinho, Nepstad, Anderson, Rodrigues, Garcia et al., 2010).
Sites can be selected to create barriers in order to block the advance of deforestation. For example, in 2004, a 30,000 km2 “mosaic” of protected areas was created by the state of Amazonas to block entry of deforestation from Mato Grosso. Another example is the “armored zone” (zona blindada) along the proposed BR-319 (Manaus-Porto Velho) Highway. This is supposed to act, in a way similar to the armor on a tank, to prevent deforestation from perforating the barrier of reserves that are parallel to the highway. Although the reserves themselves may resist deforestation, planned side roads cutting through them would simply take deforesters into unprotected areas beyond the line of “armor” (Fearnside, Graça, Keizer, Maldonado, Barbosa, & Nogueira, 2009). Reserves are needed in the large area that would be exposed to this migration to the west of the Purus River (Graça, dos Santos M. A., Jr., Rocha, Fearnside, Emilio, Menger et al., 2014). Similarly, new reserves are needed in Roraima in areas that would receive migrants from the arc of deforestation as a result of opening the BR-319 (Barni, Fearnside, & Graça, 2015).
The creation of protected areas is, in many cases, a question of now or never. Once population moves into and claims an area, it becomes politically impossible to create protected areas. One of the choices that must always be made is whether to prioritize the creation of areas in the integral-protection category or in the sustainable-use category. Because it is much easier to obtain political and local support for creating sustainable-use areas, these often best serve the objective of obtaining large areas of protected forest within a time frame that avoids losing the option to create a protected area altogether (Fearnside, 2011). Depending on circumstances, creating integral-protection protected areas can also result in social injustices. However, it is also possible to go too far in the direction of reduced protection in order to garner support. The SNUC includes as one of its protected area types the “environmental protection area” (APA). There are almost no restrictions on APAs, in practice, including in urban areas. Creating APAs may result in maps with large areas colored in green, but it does little to actually protect the forest. Instead, it offers an easy escape for interest groups intent on averting protected-area restrictions because they can always demand that a proposed protected area be an APA instead of one of the types with more real protection (e.g., Câmara, 2000; Pádua, 2011).
Protected areas are not as protected as is often assumed (Table 1). Deforestation takes place within these areas, including indigenous areas (Fearnside, 2005b; Nogueira, Yanai, Vasconcelos, Graça, & Fearnside, 2017). There is also a tendency for the government to downgrade or downsize existing reserves, or even to revoke them completely (Bernard, Penna, & Araújo, 2014; de Marques & Peres, 2015). An example is provided by the protected areas that would be affected by planned dams in the Tapajós River basin (Fearnside, 2015a). Another is a proposed law by legislators from the state of Amazonas to revoke protection from 10,000 km2 of the “mosaic” of conservation units in the deforestation hotspot in the southern part of the state (Instituto Socioambiental, 2017a, 2017b).
Table 1. Protected Areas in Legal Amazonia(a)
Number of areas
Total area (km2)
Original vegetation(b) in 2014 (km2)
Percent cleared (b) (%)
Integral protection conservation units
Sustainable use conservation units
Integral protection conservation units
Environmental protection areas (APAs)
Sustainable use conservation units excluding APAs
a Values summed from Nogueira et al. (2017), which includes area and carbon data for each protected area.
b All original vegetation, including nonforest vegetation, such as cerrado (savanna).
Since both the human and financial resources for protected areas are always very limited, one of the perennial dilemmas is whether to give priority to creating new areas or to invest in staffing and defending existing areas. So long as Brazilian Amazonia continues to have large areas of unprotected forest on government land, the better option is to maximize the creation of new areas, even if they are “paper parks” with only a token government presence. This is needed to obtain larger areas before the opportunities to do so are foreclosed. Even “paper parks” have a significant effect in inhibiting deforestation because their legal status makes it far less likely that potential invaders will be successful in gaining title to the land in the future, as compared to their invading forest in an area that is not legally protected.
Depending on whether a protected area is near or far from the deforestation frontier, its effect on deforestation will either be immediate or delayed. The priority for reserve creation will depend on the objectives that motivate the decision. It is often said that those who are primarily concerned with maintaining biodiversity and those who are primarily concerned with avoiding climate change share a natural alliance in that protecting tropical forest achieves both goals. However, this identity of interests can break down when choices must be made. If the priority is protecting biodiversity, the objective is likely to be seen in terms of a measure such as the number of species that will be maintained over a long time—theoretically permanently—making the creation of large, inexpensive reserves far from the frontier the best choice (Fearnside, 2003a; Fearnside & Ferraz, 1995). In terms of climate change, the priority is likely to be measured in terms of reduced emissions over a short time period, making reserves nearer to the frontier the best choice. The financial costs and other obstacles at each distance from the frontier will determine the ideal location, which is likely not to be at either extreme in terms of distance from the frontier. In practice, the type of protected area is associated with distance from the frontier, and sustainable-use areas are more likely to be closer to the frontier than are integral-protection areas, giving the former a greater short-term effect in avoiding deforestation (Pfaff, Robalino, Lima, Sandoval, & Herrera, 2014).
The 2015 Paris accords have fundamentally changed the criteria for choices based on climate benefits: the objective is expressed as keeping mean global temperature from rising above a value “well below” the benchmark of 2 °C over the preindustrial average, whereas the objective was previously expressed in terms of Article 2 of the Climate Convention, which specifies “stabilization” of greenhouse-gas concentrations at a level to avoid “dangerous interference with the global climate system.” Because stabilization can take many years, even centuries, this is an entirely different time scale. Assuming that diplomats and decision-makers are serious about complying with the Paris accords, what counts is what happens in the next 20 years. In terms of protected areas, relevant benefits will be from those near the frontier. The fact that many protected areas are far from the frontier means that their climatic benefit is decreased by the Paris accord relative to other forms of mitigation that yield quicker returns. Another factor decreasing the importance of protected areas is the effect of “leakage,” or the displacement of impacts, in this case deforestation, to locations beyond the boundaries of a mitigation project. Leakage from reserve creation is of two types: “in-to-out” leakage, in which deforesters leave the area to continue clearing forest elsewhere, and “out-to-out” leakage, in which potential squatters and grileiros choose areas elsewhere in the forest to invade because the reserve decreases their chances of gaining title. Deforestation that has been displaced by leakage will continue until the available forest is exhausted in the landscape outside the reserve, after which the climatic benefit that was lost through leakage will be recovered assuming that the reserve is effective in excluding deforesters (Fearnside, 2009a). The impact of leakage on decreasing the climatic value of a reserve increases with increasing value attributed to time, as through a discount rate. Reserves as a mitigation option therefore decrease in value with the Paris accords. By contrast, other options substantially increase in value, such as refraining from building hydroelectric dams, which are an energy source that has very high initial emissions and that emits methane, a short-lived gas with high impact while it remains in the atmosphere (Fearnside, 2015c, 2017c).
Contain Infrastructure Projects
An essential part of any plan to contain deforestation in Amazonia is to limit new infrastructure projects, such as roads and dams. This often goes unmentioned in plans for limiting deforestation, such as Brazil’s PPCDAm (Ministério do Meio Ambiente, 2013) and National Plan for Climate Change (Comitê Interministerial sobre Mudança do Clima, 2008). Vast plans for new infrastructure imply more, not less, deforestation—one cannot expect deforestation to decrease if new projects go ahead regardless of impacts. The pattern of assuming that unrealistic governance scenarios will play out in practice is a formula for environmental disaster (Fearnside, 2007; Fearnside & Graça, 2009).
Decisions on new infrastructure represent a key element that is in the control of the government. The decision to build a road, for example, is made by a handful of government authorities, as contrasted with the individual decisions of the thousands of actors who will determine the deforestation consequences once the road is built. The decision-making process for infrastructure projects is therefore critical. Decision-making is distinct from licensing, although licensing is also important. At present, the role of environmental licensing in Brazil is largely limited to suggesting minor changes in project design or compensation measures, not to comment on the existence or not of the infrastructure project in question. This system need to reformed to ensure that environmental and social costs and benefits are transparently assessed and democratically debated before the actual decision to build a project is made (e.g., Fearnside, 2014a). Among the changes needed to create a more rational decision-making system is to remove the underlying causes of the current bias in favor large, expensive projects regardless of their impacts. This requires making changes in the regulation of political campaign contributions (Fearnside, 2016d). It also requires revocation of the “security-suspension” laws stemming from Brazil’s military dictatorship period that allow any judicial decision to be overturned in the interests of the “public economy” (Fearnside, 2015c). Despite its problems, Brazil’s environmental licensing system is far better than the practices that were used before this system was implemented, in 1986; however, environmental licensing faces a series of immediate threats that could result in its being effectively abolished by the National Congress (Fearnside, 2016b; Ferreira et al., 2014).
Abandon Myths That Divert Efforts to Contain Deforestation
A variety of myths tend to divert efforts to control forest loss in directions that fail to achieve this objective or that are counterproductive. One is the idea that “sustainable logging,” or “sustainable forest management,” will motivate long-term maintenance of the forest. It is simply assumed that what is called “sustainable forest management” is really sustainable (e.g., Ministério do Meio Ambiente & Ministério de Ciência, Tecnologia e Inovação, 2014). However, fundamental contradictions result in the behavior of the managers not being sustainable, no matter what their discourse or promises may be (Fearnside, 1989d, 2003a). This is because trees in tropical forests grow at rates that are limited by biology and have no relation to the rates at which money can be made in alternative investments. In practice, the trees are in competition with a wide range of other possible investments (including first-cycle forest-management projects elsewhere), and it is more profitable for the manager to exploit the potentially renewable resource as quickly as possible and then to invest the proceeds in an option with a faster return elsewhere (e.g., Clark, 1973, 1976). The first cycle, which is what is in course in virtually all forest-management projects in Brazilian Amazonia, is inherently more profitable than subsequent cycles because the large forest trees that have been growing for centuries at no cost to the manager are there for the harvesting; whereas the situation will change in a future equilibrium when the manager can only harvest what grows while the management area is being defended and maintained. In addition, based on the population biology of the trees, the current rules for management projects are unlikely to maintain forest indefinitely even if they are followed as is theoretically envisioned (Kageyama, 2000). Furthermore, the theoretical 30-year cycle in terra firme (unflooded upland) forests has been subverted by the inclusion of loopholes that imply a virtual zero probability of continuation after the first cycle. An example is provided by a project in Acre managing 12,000 ha (Fearnside, 2015f). Instead of dividing the area into 30 plots, one to be harvested in each year of the cycle, the manager was allowed to harvest the entire area in only six years. Theoretically, the land would have then sat unused for 24 years until the second cycle began. The chance of this happening was obviously slim, even less so given that the area was later sold for a settlement project. The chances are even lower in the case of small management projects (up to 100 ha under management) in the state of Amazonas, which allow the entire area to be harvested in the first year, to theoretically be followed by a 29-year wait for the start of another cycle.
Another myth that diverts efforts to contain deforestation is the notion that intensification of agriculture and ranching will cause actors to stop deforesting. There are good reasons for intensification, but land sparing is not one of them. The subsidies and marketing advantages that can be garnered from this discourse represent attractions for endorsing this path, which nevertheless goes against economic logic. The idea that people’s ambitions are limited by a “full-stomach” effect, when one stops expanding production once minimal requirements are met, does not apply to individuals who are integrated into modern economies, as are almost all actors in Amazonian deforestation. A number of authors have proposed land sparing through intensification by (Sánchez, Bandy, Villachica, & Nicholaides, 1982; Strassburg, Latawiec, Barioni, Nobre, da Silva, V.P., Valentim et al., 2014; Zarin, Harris, Baccini, Aksenov, Hansen, Azevedo-Ramos et al., 2016), but the prospects that this strategy will have the desired environmental result are poor (Fearnside, 1987c). Unfortunately, there is no evidence that the response to a productivity increase would be to restore forest. If pasture were to produce more, then the ranchers would simply export the excess—not keep the total production of their properties constant and reduce pasture areas. In fact, since the more highly productive pastures would presumably be more profitable than the present ones, the tendency would be to do just the opposite—expand the area of pasture by clearing more (Fearnside, 2002; Kaimowitz & Angelsen, 2008). Pasture area in Brazil is not restrained, either by a limited desire of ranchers to make more money or by global markets for beef.
Another diversion of efforts to contain Amazonian deforestation is investment in subsidizing what is known in Brazil as “recuperation of degraded areas,” that is, restoring tree cover in nonproductive areas that have already been deforested. This should not be a current priority because, under current conditions in Amazonia, it is much more expensive to recuperate a hectare of forest than to avoid a hectare of deforestation, and the benefits in terms of both carbon and biodiversity are much less (Fearnside, 2003a). Severe limits restrict the recuperation of degraded lands through sustainable uses such as agroforestry (Fearnside, 1995). One is the difference in scale between the extent of degraded pastures in Amazonia and the capacity of markets and input sources to support agroforestry. Another is the logic from the viewpoint of a farmer making decisions on agroforestry: if a hectare is planted in a degraded pasture, it will produce very little compared to what it would produce if another hectare of forest is cleared and planted.
It is not enough to prohibit deforestation and punish violations—alternatives must be offered for supporting the small farmers who sustain themselves by clearing forest, for both subsistence and commercial production. However, there is no need to provide such alternatives for investors (Fearnside, 1989b). These larger operators can fend for themselves very well by switching to other types of investment without a need for subsidies with funds intended for environmental purposes.
The current economy of rural Amazonia is almost entirely based on destruction of the forest: selling timber and replacing forest with crops or pasture. Tapping the value of the environmental services of the forest as an alternative basis for the rural economy. Even though the environmental services, such as avoiding global warming, recycling water, and maintaining biodiversity, are worth much more to human society than the money gained from destroying the forest, the institutional mechanisms needed to transform these services into a monetary flow and to use this flow to support the rural population without provoking perverse social effects are lacking. Some progress has been made toward the goal of obtaining monetary flows through international negotiations under the Climate Convention, but the social side of this mechanism—how money would be used once obtained—is completely unresolved. Payment for environmental services (PES) is viewed as the most direct way of providing conservation incentives and avoiding perverse effects on equity (Börner, Wunder, Wertz-Kanounnikoff, Tito, Pereira, & Nascimento, 2010; Ferraro & Kiss, 2002). Land-tenure regularization is an unavoidable prerequisite for PES to function (Wunder, Börner, Tito, & Pereira, 2009), which creates both dangers and new opportunities to induce environmental compliance (Duchelle, Cromberg, Gebara, Guerra, Melo, Larson et al., 2014). In terms of cost effectiveness, command and control is still the cheapest option for reducing deforestation in Brazilian Amazonia, but PES, if directed to small actors, offers a way of reducing or avoiding negative social impacts (Börner, Marinho, & Wunder, 2015).
One cannot simply pay people for doing nothing or distribute money and goods to local communities without creating conflicts and destroying cultures. The recent disastrous case of compensation distributions to indigenous communities affected by the Belo Monte Dam offers a concrete example (Fearnside, 2017a, 2017b; Heurich, 2013). Subsidizing purchases of nontimber forest products from extractive reserves has been suggested as one possible support mechanism (Fearnside, 1989c). Current discussions of REDD+ (Reducing Emissions from Deforestation and Degradation) involve a series of controversies, including questions of how accounting for carbon benefits is done at both the proposal stage and later stages for verification and payment (Fearnside, 2012a, 2012b; Vitel, Carrero, Cenamo, Leroy, Graça, & Fearnside, 2013; Yanai, Fearnside, Graça, & Nogueira, 2012). Resolution of the various open questions regarding the quantification and institutional mechanisms for rewarding the environmental services of Amazonian forests, including their carbon benefits, remains a top priority for creating an alternative to deforestation on the scale and within the time frame that this alternative is needed (Fearnside, 2013b).
Is Brazil’s Amazonian Deforestation “Development”?
The term “development” implies a change with an effect that increases human well-being. This is not to be confused with “growth,” which refers to an increase in the throughput of matter and energy in a human society and may or may not benefit well-being (Daly, 1996). Fortunately, development does not necessarily require growth, which is subject to sever planetary limits (Steffen, Richardson, Rockstrom, Cornell, Fetzer, Bennett et al., 2015). Limiting factors within Amazonia restrain many types of use (Fearnside, 1986b, 1997c; Fearnside & Leal Filho, 2001). To be considered sustainable development, the productive systems must continue to yield their benefits for a very long time, theoretically indefinitely, the Brundtland Commission’s (1987) caveat regarding nonrenewable resources notwithstanding. Many of the most common land uses, such as extensive cattle pasture, are unsustainable (Fearnside, 1983). In the case of cattle pasture, which dominates deforested areas in most of Brazilian Amazonia (Fearnside, 1996; INPE, 2014b), the human population supported per unit area of deforestation is minimal: the productivity and financial benefit are small, and there is even less of a local benefit (Fearnside, 2005a, 2013a, 2016c). The question of who benefits is, of course, critical to defining what is development; this author has argued that the people living in Amazonia must be benefited in order for undertakings in the region to be considered “development” (Fearnside, 1997b).
The sequence of changes in human well-being as Amazon deforestation progresses has been characterized as a boom-and-bust pattern, in which indicators of well-being increase in the early phase of deforestation, followed by a decline after the frontier stage has passed so that the median HDI by municipality (county) returns to a low level, similar to that before the deforestation boom (Rodrigues et al., 2009). This conclusion was based on a cross-sectional study of statistics by the United Nations Development Programme (UNDP) for 286 municipalities from 1991 to 2000. Celentano, Sills, Sales, and Verissimo (2012), using the same data source, reached a similar conclusion based on 399 municipalities (that also went up to 2000), although these authors also found that HDI could rise again after the crash in a second turning point. The boom-and-bust pattern has been contested by Weinhold, Reis, and Vale (2015), who found that the pattern in the cross-sectional data is explained by spatial correlation, because the pre-frontier phase is largely represented by poor municipalities with abundant forest in the western part of the state of Amazonas, while the postdeforestation “bust” is largely represented by heavily deforested areas in the state of Maranhão, where the persistent poverty of northeastern Brazil explains the low HDI rather than the assumed sequence based on municipalities elsewhere. The boom-bust effect disappears without these municipalities in the analysis, and extending the analysis to 2010 also eliminates the effect. Weinhold et al. (2015) also emphasize that none of the five existing longitudinal studies of specific cases shows a boom-and-bust pattern. Caviglia-Harris et al. (2016) also analyzed these municipal data for 1991, 2000, and 2010, finding that cross-sectional analysis shows a boom-and-bust but that a panel analysis indicates instead a “decoupling” of HDI from deforestation.
An important aspect of municipal-level HDI data is that only the population that is present at the time of each census is considered. There are both winners and losers with the arrival and with the passage of the deforestation frontier. Many of the transformations involve a substitution of the resident population, with one set of residents being either expelled or bought out by the next. For example, small farmers may be replaced by cattle ranchers, who may at a later phase sell their land to soybean planters from other parts of the country, as has occurred in many areas in Mato Grosso. The municipalities dominated by soybeans in Mato Grosso have some of the highest HDI values in Brazil, but the initial population of these areas is no longer present and is not among the beneficiaries: only the winners remain (Fearnside & Figueiredo, 2016).
Both extensive cattle ranching and soybeans occupy vast areas but support few people as compared to family agriculture. However, in the approximately 3,000 settlements that have been established to support small farmers (Yanai et al., 2017) the sequence of developments is not so different in environmental terms. The vast majority of the land that the settlers deforest soon becomes cattle pasture, even if it is first planted a time or two in annual food crops (e.g., Diniz, Hoogstra-Klein, Kok, & Arts, 2013; Fearnside, 1986b, 1989e). Altering this pattern will require changing the way land tenure is established, eliminating the tradition of legalizing invasions whether by small squatters or large grileiros (Fearnside, 1979, 2001b). It will also require an end to using Amazonia as a dumping ground for the country’s social problems, such as the presence of millions of poor, landless farmers. Brazil’s Amazon forest was originally the size of Western Europe, and the 784,666 km2 that had been deforested by 2016 is the size of France and the United Kingdom combined. This alone is more than sufficient to feed the Brazilian population. Brazil is the world’s largest exporter of beef, and one of the top exporters of soybeans, meaning that the production of these products already far exceeds the amounts needed to feed the country’s population, and every hectare that is now being deforested for pasture and soy is for export. This means that deforestation can be reduced without affecting Brazil’s food supply. In other words, “zero deforestation” is possible.
The author’s research is supported by the National Council for Scientific and Technological Development (CNPq: Proc. 304020/2010-9; 573810/2008-7), the Foundation for Support of Research in Amazonas (FAPEAM: Proc. 708565), the National Institute for Research in Amazonia (INPA: PRJ15.125) and the Brazilian Research Network on Climate Change (RedeClima; FINEP: 01.13.0353-00). No funds are received from corporate sources, such as those for soy, beef, or timber. Reviewer and editor comments were helpful.
- Adario, P. (2016, July 27). The soy moratorium, 10 years on: How one commitment is stopping Amazon destruction (Web blog post). Amsterdam, The Netherlands: Greenpeace International. Retrieved from http://www.greenpeace.org/international/en/news/Blogs/makingwaves/the-soy-moratorium-10-year-anniversary-stopping-amazon-destruction/blog/57127/.
- Alencar, A. A., Nepstad, D. C., & Diaz, M. C. V. (2006). Forest understory fire in the Brazilian Amazon in ENSO and non-ENSO years: Area burned and committed carbon emissions. Earth Interactions, 10(6), 1–17.
- Antunes, A. P., Fewster, R. M., Venticinque, E. M., Peres, C. A., Levi, T., Rohe, F., & Shepard, G. H., Jr. (2016). Empty forest or empty rivers? A century of commercial hunting in Amazonia. Science Advances, 2(10), e1600936.
- Aragão, L. E. O. C., & Shimabukuro, Y. E. (2010). The incidence of fire in Amazonian forests with implications for REDD. Science, 328, 1275–1278.
- Arima, E., Barreto, P., & Brito, M. (2005). Pecuária na Amazônia: Tendências e implicações para a conserva ambiental. Belém, Brazil: Instituto do Homem e Meio Ambiente da Amazônia (IMAZON). Retrieved from http://imazon.org.br/PDFimazon/Portugues/livros/ecuaria-na-amazonia-tendencias-e-implicacoes-para.pdf.
- Arima, E. Y., Barreto, P., Araujo, E., & Soares-Filho, B. (2014). Public policies can reduce tropical deforestation: Lessons and challenges from Brazil. Land Use Policy, 41, 465–473.
- Arima, E. Y., Richards, P., Walker, R., & Caldas, M. M. (2011). Statistical confirmation of indirect land use change in the Brazilian Amazon. Environmental Research Letters, 6, 024010.
- Arima, E. Y., Walker, R., Perz, S. G., & Caldas, M. (2005). Loggers and forest fragmentation: Behavioral models of road building in the Amazon basin. Annals of the Association of American Geographers, 95, 525–541.
- Arraut, J. M., Nobre, C. A., Barbosa, H. M., Obregon, G., & Marengo, J. A. (2012). Aerial rivers and lakes: Looking at large-scale moisture transport and its relation to Amazonia and to subtropical rainfall in South America. Journal of Climate, 25, 543–556.
- Asner, G., Knapp, D., Broadbent, E., Oliveira, P., Keller, M., & Silva, J. (2005). Selective logging in the Brazilian Amazon. Science, 310, 480–482.
- Assunção, J., Gandour, C., & Rocha, R. (2013). DETERing deforestation in the Amazon: Environmental monitoring and law enforcement. Report of the Climate Policy Initiative, Rio de Janeiro, Brazil. Retrieved from http://climatepolicyinitiative.org/wp-content/uploads/2013/05/DETERring-Deforestation-in-the-Brazilian-Amazon-Environmental-Monitoring-and-Law-Enforcement-Technical-Paper.pdf.
- Assunção, J., Gandour, C. C., &. Rocha, R. (2015). Deforestation slowdown in the legal Amazon: Prices or policies?. Environment and Development Economics, 20, 697–722.
- Barbosa, R. I., & Fearnside, P. M. (1999). Incêndios na Amazônia Brasileira: Estimativa da emissão de gases do efeito estufa pela queima de diferentes ecossistemas de Roraima na passagem do evento “El Niño” (1997/98). Acta Amazonica, 29, 513–534. English version available at http://philip.inpa.gov.br/publ_livres/mss%20and%20in%20press/RR-Fire-Acta-engl.pdf.
- Barlow, J., & Peres, C. A. (2006). Consequences of cryptic and recurring fire disturbances for ecosystem structure and biodiversity in Amazonian forests. In W. F. Laurance & C. A. Peres (Eds.), Emerging threats to tropical forests (pp. 225–240). Chicago: University of Chicago Press.
- Barlow, J., & Peres, C. A. (2008). Fire-mediated dieback and compositional cascade in an Amazonian forest. Philosophical Transactions of the Royal Society B, 363, 1787–1794.
- Barlow, J., Peres, C. A., Lagan, B. O., & Haugaasen, T. (2003). Large tree mortality and the decline of forest biomass following Amazonian wildfires. Ecology Letters, 6(1), 6–8.
- Barlow, J., Lennox, G. D., Ferreira, J., Berenguer, E., Lees, A. C., MacNally, R., et al. (2016). Anthropogenic disturbance in tropical forests can double biodiversity loss from deforestation. Nature, 535, 144–147.
- Barni, P. E., Fearnside, P. M., & Graça, P. M. L. A. (2015). Simulating deforestation and carbon loss in Amazonia: Impacts in Brazil’s Roraima state from reconstructing Highway BR-319 (Manaus-Porto Velho). Environmental Management, 55, 259–278.
- Barona, E., Ramankutty, N., Hyman, G., & Coomes, O. T. (2010). The role of pasture and soybean in deforestation of the Brazilian Amazon. Environmental Research Letters, 5(2), 024002.
- Barreto, P., Brandão A., Jr., Martins, H., Silva, D., Souza C., Jr., Sales, M., et al. (2011). Risco de desmatamento associado à hidrelétrica de Belo Monte. Belém, Brazil: Instituto do Homem e Meio Ambiente da Amazônia (IMAZON). Retrieved from http://imazon.org.br/PDFimazon/Portugues/livros/RiscoDesmat_BeloMonte_25agosto2011.pdf.
- Barreto, P., Brandão A., Jr., Silva, S. B., & Souza, C., Jr. (2014). O risco de desmatamento associado a doze hidrelétricas na Amazônia. In W. C. de Sousa Jr. (Ed.), Tapajós: Hidrelétricas, infraestrutura e caos; elementos para a governança da sustentabilidade em uma região singular (pp. 147–173). São Paulo, Brazil: Instituto Tecnológico de Aeronáutica. Retrieved from http://www.bibl.ita.br/download/Tapajos_Ebook.pdf.
- Berenguer, E., Ferreira, J., Gardner, T. A., Aragão, L. E. O. C., de Camargo, P. B., Cerri, C. E., et al. (2014). A large-scale field assessment of carbon stocks in human-modified tropical forests. Global Change Biology, 20, 3713–3726.
- Bernard, E., Penna, L. A. O., & Araújo, E. (2014). Downgrading, downsizing, degazettement, and reclassification of protected areas in Brazil. Conservation Biology, 28, 939–950.
- Binswanger, H. P. (1991). Brazilian policies that encourage deforestation in the Amazon. World Development, 19, 821–829.
- Börner, J., Kis-Katos, K., Hargrave, J., & König, K. (2015). Post-crackdown effectiveness of field-based forest law enforcement in the Brazilian Amazon. PLoS One, 10(4), e0121544.
- Börner, J., Marinho, E., & Wunder, S. (2015). Mixing carrots and sticks to conserve forests in the Brazilian Amazon: A spatial probabilistic modeling approach. PLoS One, 10(2), e0116846.
- Börner, J., Wunder, S., Wertz-Kanounnikoff, S., Tito, M. R., Pereira, L., & Nascimento, N. (2010). Direct conservation payments in the Brazilian Amazon: Scope and equity implications. Ecological Economics, 69, 1272–1282.
- Bowman, M. S., Soares-Filho, B. S., Merry, F. D., Nepstad, D. C., Rodrigues, H., & Almeida, O. T. (2012). Persistence of cattle ranching in the Brazilian Amazon: A spatial analysis of the rationale for beef production. Land Use Policy, 29, 558–568.
- Brown, S., & Zarin, D. (2013). What does zero deforestation mean?. Science, 342, 805–807.
- Brundtland Commission. (1987). Our common future. Oxford: Oxford University Press.
- Caldas, M. M., Simmons, C., Walker, R., Perz, S., Aldrich, S., Pereira, R., et al. (2010). Settlement formation and land cover and land use change: A case study in the Brazilian Amazon. Journal of Latin American Geography, 9(1), 125–144.
- Caldas, M. M., Walker, R., Arima, E., Perz, S., Aldrich, S., & Simmons, C. (2007). Theorizing land cover and land use change: The peasant economy of Amazonian deforestation. Annals of the Association of American Geographers, 97, 86–110.
- Câmara, I. (2000, December 5). Para que servem as APAs? O Globo. Retrieved from https://documentacao.socioambiental.org/noticias/anexo_noticia/12876_20100602_161947.pdf.
- Campos, M. T., & Nepstad, D. C. (2006). Smallholders, the Amazon’s new conservationists. Conservation Biology, 20, 1553–1556.
- Canal Rural. (2017). Comissão aprova pastagem em área de reserva legal. Retrieved from http://www.canalrural.com.br/noticias/pecuaria/comissao-aprova-pastagem-area-reserva-legal-66219#article_selector.
- Cardoso, D., Ribeiro, J., Salomão, R., Fonseca, A., & Souza, C., Jr. (2017). Degradação florestal no estado do Pará (agosto de 2015 a julho de 2016). Belém, Brazil: Instituto do Homem e Meio Ambiente da Amazônia (IMAZON). Retrieved from http://imazon.org.br/publicacoes/degradacao-florestal-no-estado-do-para-agosto-de-2015-a-julho-de-2016/.
- Carrero, G. C., & Fearnside, P. M. (2011). Forest clearing dynamics and the expansion of land holdings in Apuí: A deforestation hotspot on Brazil’s Transamazon Highway. Ecology and Society, 16(2), 26. Retrieved from http://www.ecologyandsociety.org/vol16/iss2/art26/.
- Caviglia-Harris, J., Sills, E., Bell, A., Harris, D., Mullan, K., & Roberts, D. (2016). Busting the boom-bust pattern of development in the Brazilian Amazon. World Development, 79, 82–96.
- Celentano, D., Sills, E., Sales, M., & Verissimo, A. (2012). Welfare outcomes and the advance of the deforestation frontier in the Brazilian Amazon. World Development, 40, 850–864.
- Charoux, A. (2016). The cattle battle: How Brazil’s largest supermarket is stepping up to stop Amazon destruction for beef. Washington, DC: Greenpeace. Retrieved from http://www.greenpeace.org/usa/cattle-deforestation-amazon-brazil-beef-supermarket/.
- Cisneros, E., Zhou, S. L., & Börner, J. (2015). Naming and shaming for conservation: Evidence from the Brazilian Amazon. PLoS One, 10(9), e0136402.
- Clark, C. W. (1973). The economics of overexploitation. Science, 181, 630–634.
- Clark, C. W. (1976). Mathematical bioeconomics: The optimal management of renewable resources. New York: Wiley-Interscience.
- Cochrane, M. A., Alencar, A., Schulze, M. D., Souza, C. M., Nepstad, D. C., Lefebvre, P., et al. (1999). Positive feedbacks in the fire dynamic of closed canopy tropical forests. Science, 284, 832–1835.
- Comitê Interministerial sobre Mudança do Clima. (2008). Plano nacional sobre mudança do Clima—PNMC—Brasil. Brasília, Brazil: Ministério do Meio Ambiente. Retrieved from http://www.mma.gov.br/estruturas/smcq_climaticas/_arquivos/plano_nacional_mudanca_clima.pdf.
- Daly, H. E. (1996). Beyond growth: The economics of sustainable development. Boston: Beacon.
- de Marques, A. A. B., & Peres, C. A. (2015). Pervasive legal threats to protected areas in Brazil. Oryx, 49, 25–29.
- Diniz, C. G., Souza, A. A. D. A., Santos, D.C., Dias, M. C., da Luz, N. C., de Moraes, D. R. V., et al. (2015). DETER-B: The new Amazon near real-time deforestation detection system. IEEE Journal of Selected Topics in Applied Earth Observations and Remote Sensing, 8, 3619–3628.
- Diniz, F. H., Hoogstra-Klein, M. A., Kok, K., & Arts, B. (2013). Livelihood strategies in settlement projects in the Brazilian Amazon: Determining drivers and factors within the Agrarian Reform Program. Journal of Rural Studies, 32, 196–207.
- Duchelle, A. E., Cromberg, M., Gebara, M. F., Guerra, R., Melo, R., Larson, A., . . . May, G. (2014). Linking forest tenure reform, environmental compliance, and incentives: Lessons from REDD + initiatives in the Brazilian Amazon. World Development, 55, 53–67.
- Escada, M. I. S., Vieira, I. C. G., Amaral, S., Araújo, R., da Veiga, J. B., Aguiar, A. P. D., et al. (2005). Padrões e processos de ocupação nas novas fronteiras da Amazônia: O interflúvio do Xingu/Iriri. Estudos Avançados, 19(54), 9–23.
- Faminow, M. D. 1998. Cattle, deforestation, and development in the Amazon: An economic, agronomic, and environmental perspective. Wallingford, U.K.: CAB International.
- Faria, W. R., & Almeida, A. N. (2016). Relationship between openness to trade and deforestation: Empirical evidence from the Brazilian Amazon. Ecological Economics, 121, 85–97.
- Fearnside, P. M. (1979). The development of the Amazon rain forest: Priority problems for the formulation of guidelines. Interciencia, 4(6), 338–343.
- Fearnside, P. M. (1983). Development alternatives in the Brazilian Amazon: An ecological evaluation. Interciencia, 8(2), 65–78.
- Fearnside, P. M. (1984). Land clearing behaviour in small farmer settlement schemes in the Brazilian Amazon and its relation to human carrying capacity. In A. C. Chadwick & S. L. Sutton (Eds.), Tropical rain forest: The Leeds symposium (pp. 255–271). Leeds, U.K.: Leeds Philosophical and Literary Society.
- Fearnside, P. M. (1985). Agriculture in Amazonia. In G. T. Prance & T. E. Lovejoy (Eds.), Key environments: Amazonia (pp. 393–418). Oxford: Pergamon.
- Fearnside, P. M. (1986a). Agricultural plans for Brazil’s Grande Carajás Program: Lost opportunity for sustainable development? World Development, 14, 385–409.
- Fearnside, P. M. (1986b). Human carrying capacity of the Brazilian rainforest. New York: Columbia University Press.
- Fearnside, P. M. (1987a). Causes of deforestation in the Brazilian Amazon. In R. F. Dickinson (Ed.), The geophysiology of Amazonia: Vegetation and climate interactions (pp. 37–61). New York: Wiley.
- Fearnside, P. M. (1987b). Deforestation and international economic development projects in Brazilian Amazonia. Conservation Biology, 1, 214–221.
- Fearnside, P. M. (1987c). Rethinking continuous cultivation in Amazonia. BioScience, 37, 209–214.
- Fearnside, P. M. (1989a). The charcoal of Carajás: Pig‑iron smelting threatens the forests of Brazil’s eastern Amazon region. Ambio, 18, 141–143. Retrieved from http://www.jstor.org/stable/4313548.
- Fearnside, P. M. (1989b). Deforestation in the Amazon. Environment: Science and Policy for Sustainable Development, 31(7), 4–5.
- Fearnside, P. M. (1989c). Extractive reserves in Brazilian Amazonia: An opportunity to maintain tropical rain forest under sustainable use. BioScience, 39, 387–393.
- Fearnside, P. M. (1989d). Forest management in Amazonia: The need for new criteria in evaluating development options. Forest Ecology and Management, 27, 61–79.
- Fearnside, P. M. (1989e). Ocupação humana de Rondônia: Impactos, limites e planejamento (Relatórios de Pesquisa No. 5). Conselho Nacional de Desenvolvimento Científico e Tecnológico (CNPq), Brasília, Brazil. Retrieved from http://philip.inpa.gov.br/publ_livres/1989/A%20Ocupacao%20Humana%20de%20Rondonia.pdf.
- Fearnside, P. M. (1990). The rate and extent of deforestation in Brazilian Amazonia. Environmental Conservation, 17, 213–226.
- Fearnside, P. M. (1993). Deforestation in Brazilian Amazonia: The effect of population and land tenure. Ambio, 22, 537–545.
- Fearnside, P. M. (1995). Agroforestry in Brazil’s Amazonian development policy: The role and limits of a potential use for degraded lands. In M. Clüsener-Godt & I. Sachs (Eds.), Brazilian perspectives on sustainable development of the Amazon region (pp. 125–148). Paris: UNESCO.
- Fearnside, P. M. (1996). Amazonian deforestation and global warming: Carbon stocks in vegetation replacing Brazil’s Amazon forest. Forest Ecology and Management, 80, 21–34.
- Fearnside, P. M. (1997a). Environmental services as a strategy for sustainable development in rural Amazonia. Ecological Economics, 20, 53–70.
- Fearnside, P. M. (1997b). Human carrying capacity estimation in Brazilian Amazonia as a basis for sustainable development. Environmental Conservation, 24, 271–282.
- Fearnside, P. M. (1997c). Limiting factors for development of agriculture and ranching in Brazilian Amazonia. Revista Brasileira de Biologia, 57(4), 531–549.
- Fearnside, P. M. (1997d). Monitoring needs to transform Amazonian forest maintenance into a global warming mitigation option. Mitigation and Adaptation Strategies for Global Change, 2(2–3), 285–302.
- Fearnside, P. M. (1999). Biodiversity as an environmental service in Brazil’s Amazonian forests: Risks, value and conservation. Environmental Conservation, 26, 305–321.
- Fearnside, P. M. (2000). Global warming and tropical land-use change: Greenhouse gas emissions from biomass burning, decomposition and soils in forest conversion, shifting cultivation and secondary vegetation. Climatic Change, 46, 115–158.
- Fearnside, P. M. (2001a). Effects of land use and forest management on the carbon cycle in the Brazilian Amazon. Journal of Sustainable Forestry, 12(1–2), 79–97.
- Fearnside, P. M. (2001b). Land-tenure issues as factors in environmental destruction in Brazilian Amazonia: The case of southern Pará. World Development, 29, 1361–1372.
- Fearnside, P. M. (2001c). Soybean cultivation as a threat to the environment in Brazil. Environmental Conservation, 28, 23–38.
- Fearnside, P. M. (2002). Can pasture intensification discourage deforestation in the Amazon and Pantanal regions of Brazil? In C. H. Wood & R. Porro (Eds.), Deforestation and land use in the Amazon (pp. 299–314). Gainesville: University Press of Florida.
- Fearnside, P. M. (2003a). Conservation policy in Brazilian Amazonia: Understanding the dilemmas. World Development, 31, 757–779.
- Fearnside, P. M. (2003b). Deforestation control in Mato Grosso: A new model for slowing the loss of Brazil’s Amazon forest. Ambio, 32, 343–345.
- Fearnside, P. M. (2005a). Deforestation in Brazilian Amazonia: History, rates and consequences. Conservation Biology, 19, 680–688.
- Fearnside, P. M. (2005b). Indigenous peoples as providers of environmental services in Amazonia: Warning signs from Mato Grosso. In A. Hall (Ed.), Global impact, local action: New environmental policy in Latin America (pp. 187–198). London: Institute for the Study of the Americas.
- Fearnside, P. M. (2007). Brazil’s Cuiabá-Santarém (BR-163) highway: The environmental cost of paving a soybean corridor through the Amazon. Environmental Management, 39, 601–614.
- Fearnside, P. M. (2008a). Amazon forest maintenance as a source of environmental services. Anais da Academia Brasileira de Ciências, 80(1), 101–114.
- Fearnside, P. M. (2008b). The roles and movements of actors in the deforestation of Brazilian Amazonia. Ecology and Society, 13(1), 23.
- Fearnside, P. M. (2008c). Will urbanization cause deforested areas to be abandoned in Brazilian Amazonia? Environmental Conservation, 35, 197–199.
- Fearnside, P. M. (2009a). Carbon benefits from Amazonian forest reserves: Leakage accounting and the value of time. Mitigation and Adaptation Strategies for Global Change, 14, 557–567.
- Fearnside, P. M. (2009b). Potential benefits and impacts of biofuel production in the Brazilian Amazon. In E. J. Garen, & J. Mateo-Vega (Eds.), Biocombustibles y Bosques Neotropicales: Tendencias, Implicaciones, y Alternativas Emergentes / Biofuels and Neotropical Forests: Trends, Implications, and Emerging Alternatives (pp. 29–36). Proceedings of the ELTI/PRORENA Conference, December 5, 2008, Panama City, Panama. Retrieved from http://elti.yale.edu/sites/default/files/rsource_files/Biocombustibles.pdf.
- Fearnside, P. M. (2011). Strategies for social and environmental conservation in conservation units. In M. Pinedo-Vasquez, M. L. Ruffino, C. Padoch, & E. Brondizio (Eds.), The Amazonian Várzea: The decade past and the decade ahead (pp. 233–239). New York: Springer.
- Fearnside, P. M. (2012a). Brazil’s Amazon forest in mitigating global warming: Unresolved controversies. Climate Policy, 12, 70–81.
- Fearnside, P. M. (2012b). The theoretical battlefield: Accounting for the climate benefits of maintaining Brazil’s Amazon forest. Carbon Management, 3, 145–148.
- Fearnside, P. M. (2013a). The evolving context of Brazil’s environmental policies in Amazonia. Novos Cadernos NAEA, 16(2), 9–25. Available at http://www.periodicos.ufpa.br/index.php/ncn/article/view/1380/1854.
- Fearnside, P. M. (2013b). What is at stake for Brazilian Amazonia in the climate negotiations. Climatic Change, 118, 509–519.
- Fearnside, P. M. (2014a). Brazil’s Madeira River dams: A setback for environmental policy in Amazonian development. Water Alternatives, 7, 156–169. Available at http://www.water-alternatives.org/index.php/alldoc/articles/vol7/v7issue1/244-a7-1-15/file.
- Fearnside, P. M. (2014b). Impacts of Brazil’s Madeira River dams: Unlearned lessons for hydroelectric development in Amazonia. Environmental Science and Policy, 38, 164–172.
- Fearnside, P. M. (2015a). Amazon dams and waterways: Brazil’s Tapajós basin plans. Ambio, 44, 426–439.
- Fearnside, P. M. (2015b). Brazil’s São Luiz do Tapajós Dam: The art of cosmetic environmental impact assessments. Water Alternatives, 8, 373–396. Retrieved from http://www.water-alternatives.org/index.php/alldoc/articles/vol8/v8issue3/297-a8-3-5/file6.
- Fearnside, P. M. (2015c). Emissions from tropical hydropower and the IPCC. Environmental Science and Policy, 50, 225–239.
- Fearnside, P. M. (2015d). Highway construction as a force in destruction of the Amazon forest. In R. van der Ree, D. J. Smith, & C. Grilo (Eds.), Handbook of road ecology (pp. 414–424). Chichester, U.K.: Wiley.
- Fearnside, P. M. (2015e). Natural riches of Amazonia, deforestation and its consequences. Global Land Project News, 12, 22–25. Retrieved from http://philip.inpa.gov.br/publ_livres/2015/Natural_riches_of_Amazonia-Deforestation-GLPNews_2015.pdf.
- Fearnside, P. M. (2015f). Pesquisa sobre conservação na Amazônia brasileira e a sua contribuição para a manutenção da biodiversidade e uso sustentável das florestas tropicais. In I. C. G. Vieira, M. A. G. Jardim, & E. J. P. da Rocha (Eds.), Amazônia em tempo: Estudos climáticos e socioambientais (pp. 21–49). Belém, Brazil: Universidade Federal do Pará, Museu Paraense Emílio Goeldi, and Embrapa Amazônia Oriental. Available at http://www.ppgca.ufpa.br/arquivos/repositorio/TEXTODOWN/Livro%20Amaz%C3%B4nia%20em%20Tempo_Estudos%20clim%C3%A1ticos%20e%20socioambientais.pdf.
- Fearnside, P. M. (2016a, July). Brazil’s Amazonian forest carbon: The key to southern Amazonia’s significance for global climate. Regional Environmental Change. Online publication.
- Fearnside, P. M. (2016b). Brazilian politics threaten environmental policies. Science, 353, 746–748.
- Fearnside, P. M. (2016c). Environmental policy in Brazilian Amazonia: Lessons from recent history. Novos Cadernos NAEA, 19(1), 27–46. Retrieved from http://www.periodicos.ufpa.br/index.php/ncn/article/view/1379/3173.
- Fearnside, P. M. (2016d). Environmental and social impacts of hydroelectric dams in Brazilian Amazonia: Implications for the aluminum industry. World Development, 77, 48–65.
- Fearnside, P. M. (2017a). Belo Monte: Actors and arguments in the struggle over Brazil’s most controversial Amazonian dam. Die Erde, 148(1), 14–26.
- Fearnside, P. M. (2017b). Brazil’s Belo Monte dam: Lessons of an Amazonian resource struggle. Die Erde, 148(2–3), (in press).
- Fearnside, P. M. (2017c). Dams with big reservoirs: Brazil’s hydroelectric plans threaten its Paris climate commitments. The Globalist, January 29, 2017.
- Fearnside, P. M. (2017d). Resurgence of Amazon deforestation. Yale Environment, 360, 18 April 2017. Retrieved from http://e360.yale.edu/features/business-as-usual-a-resurgence-of-deforestation-in-the-brazilian-amazon.
- Fearnside, P. M., & Barbosa, R. I. (2004). Accelerating deforestation in Brazilian Amazonia: Towards answering open questions. Environmental Conservation, 31, 7–10.
- Fearnside, P. M., & Ferraz, J. (1995). A conservation gap analysis of Brazil’s Amazonian vegetation. Conservation Biology, 9, 1134–1147.
- Fearnside, P. M., & Figueiredo, A. M. R. (2016). China’s influence on deforestation in Brazilian Amazonia: A growing force in the state of Mato Grosso. In R. Ray, K. Gallagher, A. López, & C. Sanborn (Eds.), China and sustainable development in Latin America: The social and environmental dimension (pp. 229–265). New York: Anthem.
- Fearnside, P. M., Figueiredo, A. M. R., & Bonjour, S. C. M. (2013). Amazonian forest loss and the long reach of China’s influence. Environment, Development and Sustainability, 15, 325–338.
- Fearnside, P. M., & Graça, P. M. L. A. (2006). BR-319: Brazil’s Manaus-Porto Velho Highway and the potential impact of linking the arc of deforestation to central Amazonia. Environmental Management, 38, 705–716.
- Fearnside, P. M., & Graça, P. M. L. A. (2009). BR-319: A rodovia Manaus-Porto Velho e o impacto potencial de conectar o arco de desmatamento à Amazônia central. Novos Cadernos NAEA, 12(1), 19–50. Retrieved from http://www.periodicos.ufpa.br/index.php/ncn/article/viewFile/241/427.
- Fearnside, P. M., Graça, P. M. L. A., Keizer, E. W. H., Maldonado, F. D., Barbosa, R. I., & Nogueira, E. M. (2009). Modelagem de desmatamento e emissões de gases de efeito estufa na região sob influência da Rodovia Manaus-Porto Velho (BR-319). Revista Brasileira de Meteorologia, 24(2), 208–233. English translation available at http://philip.inpa.gov.br/publ_livres/mss%20and%20in%20press/RBMET-BR-319_-engl.pdf.
- Fearnside, P. M., & Leal Filho, N. (2001). Soil and development in Amazonia: Lessons from the biological dynamics of forest fragments project. In R. O. Bierregaard, C. Gascon, T. E. Lovejoy, & R. Mesquita (Eds.), Lessons from Amazonia: The ecology and conservation of a fragmented forest (pp. 291–312). New Haven, CT: Yale University Press.
- Federal Republic of Brazil. (2015). Intended nationally determined contribution towards achieving the objective of the United Nations Framework Convention on Climate Change. Retrieved from http://www4.unfccc.int/submissions/INDC/Published%20Documents/Brazil/1/BRAZIL%20iNDC%20english%20FINAL.pdf.
- Ferraro, P. J., & Kiss, A. (2002). Direct payments to conserve biodiversity. Science, 298, 1718–1719.
- Ferreira, J., Aragão, L. E. O. C., Barlow, J., Barreto, P., Berenguer, E., Bustamante, M., et al. (2014). Brazil’s environmental leadership at risk. Science, 346, 706–707.
- Ferreira, L. V., Venticinque, E., & de Almeida, S. S. (2005). O desmatamento na Amazônia e a importância das áreas protegidas. Estudos Avançados, 19(53), 1–10. Retrieved from http://www.scielo.br/pdf/ea/v19n53/24086.pdf.
- Food and Agriculture Organization of the United Nations. (2012). FRA 2015: Terms and Definitions (Forest Resources Assessment Working Paper 180). Rome, Italy. Retrieved from http://www.fao.org/docrep/017/ap862e/ap862e00.pdf.
- Foweraker, J. (1981). The struggle for land: A political economy of the pioneer frontier in Brazil: 1930 to the present. Cambridge, U.K.: Cambridge University Press.
- Gibbs, H. K., Munger, J., L’Roe, J., Barreto, P., Pereira, R., Christie, M., et al. (2016). Did ranchers and slaughterhouses respond to zero-deforestation agreements in the Brazilian Amazon?. Conservation Letters, 9, 32–42.
- Gibbs, H. K., Rausch, L., Munger, J., Schelly, I., Morton, D. C., Noojipady, P., et al. (2015). Brazil’s soy moratorium. Science, 347, 377–378.
- Godar, J., Gardner, T. A., Tizado, E. J., & Pacheco, P. (2014). Actor-specific contributions to the deforestation slowdown in the Brazilian Amazon. PNAS: Proceedings of the National Academy of Sciences of the USA, 111, 15,591–15,596.
- Godar, J., Tizado, E. J., & Pokorny, B. (2012). Who is responsible for deforestation in the Amazon? A spatially explicit analysis along the Transamazon Highway in Brazil. Forest Ecology and Management, 267, 58–73.
- Graça, P. M. L. A., dos Santos M. A., Jr., Rocha, V. M., Fearnside, P. M., Emilio, T., Menger, J. S., et al. (2014). Cenários de desmatamento para região de influência da rodovia BR-319: Perda potencial de habitats, status de proteção e ameaça para a biodiversidade. In T. Emilio & F. Luizão (Eds.), Cenários para a Amazônia: Clima, biodiversidade e uso da terra (pp. 91–101). Manaus, Brazil: Editora-INPA.
- Greenpeace. (2003). State of conflict: An investigation into the landgrabbers, loggers, and lawless frontiers in Pará state, Amazon. Report by Greenpeace International. Amsterdam, The Netherlands. Retrieved from http://www.greenpeace.org/international/press/reports/state-of-conflict.
- Greenpeace. (2006). Eating up the Amazon. Report by Greenpeace International. Amsterdam, The Netherlands. Retrieved from http://www.greenpeace.org/international/Global/international/planet-2/report/2006/7/eating-up-the-amazon.pdf.
- Greenpeace. (2009). Slaughtering the Amazon. Report by Greenpeace International. Amsterdam, The Netherlands. Retrieved from http://www.greenpeace.org/international/en/publications/reports/slaughtering-the-amazon/.
- Greenpeace. (2011). Broken promises: How the cattle industry in the Amazon is still connected to deforestation, slave labour and invasion of indigenous land. Report by Greenpeace International. Amsterdam, The Netherlands. Retrieved from http://www.greenpeace.org/international/Global/international/publications/forests/2011/12%20pages%20ingles%20baixa_FINAL.pdf.
- Hargrave, J., & Kis-Katos, K. (2013). Economic causes of deforestation in the Brazilian Amazon: A panel data analysis for the 2000s. Environmental and Resource Economics, 54, 471–494.
- Hecht, S. B. (1985). Environment, development and politics: Capital accumulation in the livestock sector in eastern Amazonia. World Development, 13, 663–684.
- Hecht, S. B. (1993). The logic of livestock and deforestation in Amazonia. BioScience, 43, 687–695.
- Hecht, S. B., Norgaard, R. B., & Possio, C. (1988). The economics of cattle ranching in eastern Amazonia. Interciencia, 13, 233–240.
- Heurich, G. O. (2013). A barragem e a canoa de Jawitï. Brasília, Brazil: Instituto Socioambiental. Retrieved from http://pib.socioambiental.org/files/file/PIB_verbetes/arawete/osaraweteeoplanoemergencial.pdf.
- Hoelle, J. (2015). Rainforest cowboys: The rise of ranching and cattle culture in western Amazonia. Austin: University of Texas Press.
- Hubbell, S. P., He, F., Condit, R., Borda-de-Água, L., Kellnert, J., & ter Steege, H. (2008). How many tree species are there in the Amazon and how many of them will go extinct?. PNAS: Proceedings of the National Academy of Science of the USA, 105(Suppl. 1), 11, 498–11,504.
- Instituto Brasileiro de Geografia e Estatística. (2012). Manual técnico da vegetação Brasileira: Sistema fitogeográfico, inventário das formações florestais e campestres, técnicas e manejo de coleções botânicas, procedimentos para mapeamentos (2d ed., p. 275). Rio de Janeiro, Brazil: IBGE.
- Instituto do Homem e Meio Ambiente da Amazônia. (2017). Transparência florestal. Belém, Brazil: IMAZON. Retrieved from http://imazon.org.br/categorias/transparencia-florestal/.
- Instituto Nacional de Pesquisas Espaciais. (2013). Metodologia para o cálculo da taxa anual de desmatamento na Amazônia legal (p. 37). São José dos Campos, Brazil: INPE. Retrieved from http://www.obt.inpe.br/prodes/metodologia_TaxaProdes.pdf.
- Instituto Nacional de Pesquisas Espaciais. (2014a). Sistema DEGRAD. São José dos Campos, Brazil: INPE, Retrieved from http://www.obt.inpe.br/degrad.
- Instituto Nacional de Pesquisas Espaciais. (2014b). Terra class. São José dos Campos, Brazil: INPE. Retrieved from http://www.inpe.br/cra/projetos_pesquisas/terraclass.php.
- Instituto Nacional de Pesquisas Espaciais. (2017a). Projeto PRODES: Monitoramento da Floresta Amazônica Brasileira por Satélite. São José dos Campos, Brazil: INPE. Retrieved from http://www.obt.inpe.br/prodes/.
- Instituto Nacional de Pesquisas Espaciais. (2017b). Sistema DETER. São José dos Campos, Brazil: INPE. Retrieved from http://www.obt.inpe.br/deter/.
- Instituto Socioambiental. (2016). Madeireiros avançam impunemente sobre os territórios indígenas e ribeirinhos, indicadores de desmatamento aumentam de novo. De Olho na Terra do Meio, 1(1), 1–4. Retrieved from https://www.socioambiental.org/sites/blog.socioambiental.org/files/nsa/arquivos/boletim_terra_do_meio_n1_jan2016.pdf.
- Instituto Socioambiental. (2017a, March 16). Mineradoras, latifundiários e senador seriam beneficiados por redução de reservas no Amazonas. Notícias Socioambientais. Retrieved from https://www.socioambiental.org/pt-br/noticias-socioambientais/mineradoras-latifundiarios-e-senador-seriam-beneficiados-por-reducao-de-reservas-no-amazonas.
- Instituto Socioambiental. (2017b). Nota Técnica sobre o Projeto de Lei de Redução e Revogação de Unidades de Conservação no Sul do Estado do Amazonas. Brasília, Brazil: Instituto Socioambiental. Retrieved from https://www.socioambiental.org/sites/blog.socioambiental.org/files/nsa/arquivos/notatecnica_pl2017reducaoucssulamazonas_institutosocioambiental_final_1.pdf.
- Intergovernmental Panel on Climate Change. (2006). 2006 IPCC guidelines for national greenhouse gas inventories, H. S. Eggleston, L. Buendia, K. Miwa, T. Ngara, & K. Tanabe (Eds.): Vol. 4: Agriculture, forestry and other land use. Kanagawa, Japan: Institute for Global Environmental Strategies. Available at http://www.ipcc-nggip.iges.or.jp.
- Jaramillo-Giraldo, C., Soares Filho, B., Ribeiro, S. M., & Gonçalves, R. C. (2017). Is it possible to make rubber extraction ecologically and economically viable in the Amazon? The Southern Acre and Chico Mendes Reserve case study. Ecological Economics, 134, 186–197.
- Kageyama, P. (2000). Uso e conservação de florestas tropicais: Qual a paradigma? In S. Watanabe (Ed.), Anais do V Simpósio de Ecossistemas Brasileiros: Conservação. 10 a 15 de outubro de 2000, Universidade Federal de Espírito Santo, Vitória, ES (Vol. 4, Publ. ACIESP No. 109-IV, pp. 72–82). São Paulo, Brazil: Academia de Ciências do Estado de São Paulo.
- Kaimowitz, D., & Angelsen, A. (2008). Will livestock intensification help save Latin America’s tropical forests?. Journal of Sustainable Forestry, 27, 6–24.
- Kaimowitz, D., Mertens, B., Wunder, S., & Pacheco, P. (2004). Hamburger connection fuels Amazon destruction: Cattle ranching and deforestation in Brazil’s Amazon. Report of the Center for International Forestry Research (CIFOR), Bogor, Indonesia. Retrieved from http://www.cifor.org/publications/pdf_files/media/Amazon.pdf.
- Kirby, K. R., Laurance, W. F., Albernaz, A. K., Schroth, G., Fearnside, P. M., Bergen, S., et al. (2006). The future of deforestation in the Brazilian Amazon. Futures, 38, 432–453.
- Lapola, D. M., Martinelli, L. A., Peres, C. A., Ometto, J. P. H. B., Ferreira, M. E., Nobre, C. A., . . . Vieira, I.C.G. (2014). Pervasive transition of the Brazilian land-use system. Nature Climate Change, 4, 27–35.
- Laurance, W. F., Albernaz, A. K. M., Schroth, G., Fearnside, P. M., Bergen, S., Venticinque, E. M., & da Costa, C. (2002). Predictors of deforestation in the Brazilian Amazon. Journal of Biogeography, 29, 737–748.
- Laurance, W. F., Cochrane, M. A., Bergen, S., Fearnside, P. M., Delamônica, P., Barber, C., et al . (2001). The future of the Brazilian Amazon. Science, 291, 438–439.
- Lewis, S. L., Brando, P. M., Phillips, O. L., van der Heijden, G. M. F., & Nepstad, D. C. (2011). The 2010 Amazon drought. Science, 331, 554.
- Lima, A., Capobianco, J. P. R., & Moutinho, P. 2009. Desmatamento na Amazônia: Medidas e efeitos do Decreto Federal 6.321/07. Belém, Brazil: Instituto de Pesquisas Ambientais da Amazônia. Retreived from http://www.climaedesmatamento.org.br/uploads/livros/f2c4f9fb5f6c9c7c2bb04e04ffad6207eb379378.pdf.
- Lopes, R. J. (2011, June 13). Datafolha indica que 80% rejeitam corte de proteção a matas. Folha de São Paulo. Retrieved from http://www1.folha.uol.com.br/ambiente/929142-datafolha-indica-que-80-rejeitam-corte-de-protecao-a-matas.shtml.
- MacMillan, G. (1995). At the end of the rainbow? Gold, land and people in the Brazilian Amazon. New York: Columbia University Press.
- Mahar, D. J. (1979). Frontier development policy in Brazil: A study of Amazonia. New York: Praeger.
- Malhi, Y., Roberts, J. T., Betts, R. A., Killeen, T. J., Li, W., & Nobre, C. A. (2008). Climate change, deforestation, and the fate of the Amazon. Science, 319, 169–172.
- Marengo, J. A., & Espinoza, J. C. (2016). Extreme seasonal droughts and floods in Amazonia: Causes, trends and impacts. International Journal of Climatology, 36, 1033–1050.
- Margulis, S. (2004). Causes of deforestation in the Brazilian Amazon (Working Paper No. 22). World Bank, Washington, DC. Retrieved from https://openknowledge.worldbank.org/bitstream/handle/10986/15060/277150PAPER0wbwp0no1022.pdf?sequence=1.
- Mattos, M. M., & Uhl, C. (1994). Economic and ecological perspectives on ranching in the eastern Amazon. World Development, 22, 145–158.
- McAlpine, C. A., Etter, A., Fearnside, P. M., Seabrook, L., & Laurance, W. F. (2009). Increasing world consumption of beef as a driver of regional and global change: A call for policy action based on evidence from Queensland (Australia), Colombia and Brazil. Global Environmental Change, 19, 21–33.
- Mertens, B., Poccard-Chapuis, R., Piketty, M.‑G., Laques, A.‑E., & Venturieri, A. (2002). Crossing spatial analyses and livestock economics to understand deforestation processes in the Brazilian Amazon: The case of Sao Felix do Xingu in South Pará. Agricultural Economics, 27, 269–294.
- Metzger, J.‑P., Lewinsohn, T., Joly, C. A., Verdade, L. M., & Rodrigues, R. R. (2010). Brazilian law: Full speed in reverse. Science, 329, 276–277.
- Michalski, F., & Peres, C. A. (2005). Anthropogenic determinants of primate and carnivore local extinctions in a fragmented forest landscape of southern Amazonia. Biological Conservation, 124, 383–396.
- Ministério do Meio Ambiente. (2013). Plano de ação para prevenção e controle do desmatamento na Amazônia Legal—PPCDAm 3ª fase (2012–2015). Brasília, Brazil: MMA. Retrieved from http://www.mma.gov.br/images/publicacoes/florestas/Catalogo/Tema3_Prevencao-Controle-Desmatamento/PPCDAm_3afase.pdf.
- Ministério do Meio Ambiente. (2015). Cadastro nacional de unidades de conservação. Brasília, Brazil. Retrieved from http://www.mma.gov.br/areas-protegidas/cadastro-nacional-de-ucs/mapas.
- Ministério do Meio Ambiente & Ministério de Ciência, Tecnologia e Inovação. (2014). Brazil’s submission of a forest reference emission level (FREL) for reducing emissions from deforestation in the Amazonia biome for REDD+ results-based payments under the UNFCCC. Brasília, Brazil: Ministério do Meio Ambiente. Retrieved from http://redd.mma.gov.br/images/Publicacoes/FREL_Complete_October31_FINAL.pdf.
- Moran, E. F. (1981). Developing the Amazon: The social and ecological consequences of government-directed colonization along Brazil’s Transamazon Highway. Bloomington: Indiana University Press.
- Morton, D. C., DeFries, R. S., Shimabukuro, Y. E., Anderson, L. O., Arai, E., del Bon Espirito-Santo, F., . . . Morisette, J. (2006). Cropland expansion changes deforestation dynamics in the southern Brazilian Amazon. PNAS: Proceedings of the National Academy of Sciences USA, 103, 14,637–14,641.
- Moura, N. G., Lees, A. C., Aleixo, A., Barlow, J., Dantas, S. M., Ferreira, J., . . . Gardner, T.A. (2014). Two hundred years of local avian extinctions in eastern Amazonia. Conservation Biology, 28, 1271–1281.
- Myers, N. (1981). The hamburger connection: How Central America’s forests became North America’s hamburgers. Ambio, 10, 3–8.
- Nepstad, D. C., Carvalho, G., Barros, A. C., Alencar, A., Capobianco, J. P., Bishop, J., . . . Prins, E. (2001). Road paving, fire regime feedbacks, and the future of Amazon forests. Forest Ecology and Management, 154, 395–407.
- Nepstad, D. C., McGrath, D., Stickler, C., Alencar, A., Azevedo, A., Swette, B., . . . Hess, L. (2014). Slowing Amazon deforestation through public policy and interventions in beef and soy supply chains. Science, 344, 1118–1123.
- Nepstad, D. C., Schwartzman, S., Bamberger, B., Santilli, M., Ray, D., Schlesinger, P., et al. (2006). Inhibition of Amazon deforestation and fire by parks and indigenous lands. Conservation Biology, 20, 65–73.
- Nepstad, D. C., Tohver, I. M., Ray, D., Moutinho, P., & Cardinot, G. (2007). Mortality of large trees and lianas following experimental drought in an Amazon forest. Ecology, 88, 2259–2269.
- Nepstad, D. C., Verissimo, A., Alencar, A., Nobre, C., Lima, E., Lefebvre, P., et al. (1999). Large-scale impoverishment of Amazonian forests by logging and fire. Nature, 398, 505–508.
- Nepstad, D. C., Irawau, S., Bezerra, T., Boyd, W., Stickler, C., Shimada, J., et al. (2013). More food, more forests, fewer emissions, better livelihoods: linking REDD+, sustainable supply chains and domestic policy in Brazil, Indonesia and Colombia. Carbon Management, 4, 639–658.
- Nogueira, E. M., Yanai, A. M., Fonseca, F. O. R., & Fearnside, P. M. (2015). Carbon stock loss from deforestation through 2013 in Brazilian Amazonia. Global Change Biology, 21, 1271–1292.
- Nogueira, E. M., Yanai, A. M., Vasconcelos, S. S., Graça, P. M. L. A., & Fearnside, P. M. (2017). Carbon stocks and losses to deforestation in protected areas in Brazilian Amazonia. Regional Environmental Change (in press).
- Nolte, C., Agrawal, A., Silvius, K. M., & Soares-Filho, B. S. (2013). Governance regime and location influence avoided deforestation success of protected areas in the Brazilian Amazon. PNAS: Proceedings of the National Academy of Sciences of the U.S.A., 110, 4956–4961.
- Nunes, S., Gardner, T., Barlow, J., Martins, H., Salomão, R., & Souza, C., Jr. (2016). Compensating for past deforestation: Assessing the legal forest surplus and deficit of the state of Pará, eastern Amazonia. Land Use Policy, 57, 749–758.
- Pádua, M. T. J. (2011). Do Sistema Nacional de Unidades de Conservação. In R. Medeiros & F. S. Araújo (Eds.), Dez anos do Sistema Nacional de Unidades de Conservação da natureza lições do passado, realizações presentes e perspectivas para o futuro (pp. 21–36). Brasília, Brazil: Ministério do Meio Ambiente. Retrieved from http://www.mma.gov.br/estruturas/240/_publicacao/240_publicacao06072011055602.pdf.
- Parry, L., Day, B., Amaral, S., & Peres, C. A. (2010). Drivers of rural exodus from Amazonian headwaters. Population and Environment, 32, 137–176.
- Peres, C. A., Emilio, T., Schietti, J., Desmoulière, S. J. M., & Levi, T. (2016). Dispersal limitation induces long-term biomass collapse in overhunted Amazonian forests. PNAS: Proceedings of the National Academy of Sciences, USA, 113, 892–897.
- Peres, C. A., & Schneider, M. (2012). Subsidized agricultural resettlements as drivers of tropical deforestation. Biological Conservation, 151, 65–68.
- Peres, C. A., & Terborgh, J. W. (1995). Amazonian nature reserves: An analysis of the defensibility status of existing conservation units and design criteria for the future. Conservation Biology, 9, 34–46.
- Pfaff, A. S. P. (1999). What drives deforestation in the Brazilian Amazon?. Journal of Environmental Economics and Management, 37, 26–43.
- Pfaff, A., Robalino, J., Lima, E., Sandoval, C., & Herrera, L. D. (2014). Governance, location and avoided deforestation from protected areas: Greater restrictions can have lower impact, due to differences in location. World Development, 55, 7–20.
- Pfaff, A., Robalino, J., Sandoval, C., & Herrera, D. (2015). Protected area types, strategies and impacts in Brazil’s Amazon: Public protected area strategies do not yield a consistent ranking of protected area types by impact. PNAS: Philosophical Transactions of the Royal Society of London B, 370, 20140273.
- Pfaff, A. S. P., Robalino, J., Walker, R., Aldrich, S., Reis, E., Perz, S., et al. (2007). Road investments, spatial spillovers, and deforestation in the Brazilian Amazon. Journal of Regional Science, 47, 109–123.
- Phillips, O. L., Aragão, L. E. O. C., Lewis, S. L., Fisher, J. B., Lloyd, J., Lopez-Gonzalez, G., et al. (2009). Drought sensitivity of the Amazon rainforest. Science, 323, 1344–1347.
- Pithan e Silva, R. O. (2016. June 22). Situação da febre aftosa no Brasil. Beef World. Retrieved from http://beefworld.com.br/noticia/situacao-da-febre-aftosa-no-brasil/.
- Rajão, R., Azevedo, A., & Stabile, M. C. C. (2012). Institutional subversion and deforestation: Learning lessons from the system for the environmental licencing of rural properties in Mato Grosso. Public Administration and Development, 32, 229–244.
- Razera, A. (2005). Dinâmica do Desmatamento em uma nova Fronteira do Sul do Amazonas: Análise da Pecuária de Corte no Município do Apuí (Master’s thesis, Instituto Nacional de Pesquisas da Amazônia and Universidade Federal do Amazonas).
- Rich, B. (2013). Foreclosing the future: The World Bank and the politics of environmental destruction. Washington, DC: Island Press.
- Richards, P. D., Walker, R., & Arima, E. Y. (2014). Spatially complex land change: The indirect effect of Brazil’s agricultural sector on land use in Amazonia. Global Environmental Change, 29, 1–9.
- Ricketts, T. H., Soares-Filho, B., da Fonseca, G. A. B., Nepstad, D., Petsonk, A., Anderson, A., et al. (2010). Indigenous lands, protected areas, and slowing climate change. PLoS Biology, 8, e1000331.
- Rodrigues, A.S.L., Ewers, R.M., Parry, L., Souza Jr., C., Veríssimo, A., & Balmford, A. (2009). Boom-and-bust development patterns across the Amazon deforestation frontier. Science, 324, 1435–1437.
- Rodrigues-Filho, S., Verburg, R., Bursztyn, M., Lindoso, D., Debortoli, N., & Vilhena, A. M. G. (2015). Election-driven weakening of deforestation control in the Brazilian Amazon. Land Use Policy, 43, 111–118.
- Rosa, I. M. D., Purves, D., Carreiras, J. M. B., & Ewers, R. M. (2014). Modelling land cover change in the Brazilian Amazon: Temporal changes in drivers and calibration issues. Regional Environmental Change, 15, 123–137.
- Rosa, I. M. D., Purves, D., Souza, C., Jr., & Ewers, R. M. (2013). Predictive modelling of contagious deforestation in the Brazilian Amazon. PLoS ONE, 8(10), e77231.
- Rosa, I. M. D., Souza, C., & Ewers, R. M. (2012). Changes in size of deforested patches in the Brazilian Amazon. Conservation Biology, 26, 932–937.
- Salisbury, D. S., & Schmink, M. (2007). Cows versus rubber: Changing livelihoods among Amazonian extractivists. Geoforum, 38, 1233–1249.
- Sánchez, P. A., Bandy, D. E., Villachica, J. H., & Nicholaides, J. J., III (1982). Amazon Basin soils: Management for continuous crop production. Science, 216, 821–827.
- Schmink, M., & Wood, C. H. (1992). Contested frontiers in Amazonia. New York: Columbia University Press.
- Schneider, M., & Peres, C. A. (2015). Environmental cost of government-sponsored agrarian settlements in Brazilian Amazonia. PLoS ONE, 10(8), e0134016.
- Schönenberg, R. (2002). Drug trafficking in the Brazilian Amazon. In C. Geffray, G. Fabre, & M. Shiray (Eds.), Globalisation, drugs and criminalisation: Final research report from Brazil, China, India and Mexico (pp. 125–148). United Nations Educational and Scientific Organization (UNESCO). Paris, France. Retrieved from http://digital-library.unesco.org/shs/most/gsdl/cgi-bin/library?e=d-000-00---0most--00-0-0--0prompt-10---4------0-1l--1-en-50---20-about---00031-001-1-0utfZz-8-00&cl=&d=HASHb5496ce0bf81c045602d82&x=1#5.
- Silvestrini, R. A., Soares-Filho, B. S., Nepstad, D., Coe, M., Rodrigues, H., & Assunção, R. (2011). Simulating fire regimes in the Amazon in response to climate change and deforestation. Ecological Applications, 21, 1573–1590.
- Simmons, C. S., Walker, R., Perz, R., Aldrich, S., Caldas, M., Pereira, R., et al. (2010). Doing it for themselves: Direct action land reform in the Brazilian Amazon. World Development, 38, 429–444.
- Smith, N. J. H. (1982). Rainforest corridors: The transamazon colonization scheme. Berkeley: University of California Press.
- Soares-Filho, B. S., Moutinho, P., Nepstad, D., Anderson, A., Rodrigues, H., Garcia, R., . . . Maretti, C. (2010). Role of Brazilian Amazon protected areas in climate change mitigation. PNAS: Proceedings of the National Academy of Sciences USA, 107, 10,821–10,826.
- Soares-Filho, B. S., Nepstad, D. C., Curran, L. M., Cerqueira, G. C., Garcia, R. A., Ramos, C. A., . . . Schlesinger, P. (2006). Modeling conservation in the Amazon Basin. Nature, 440, 520–523.
- Soares-Filho, B. S., Rajão, R., Macedo, M., Carneiro, A., Costa, W., Coe, M., . . . Alencar, A. (2014). Cracking Brazil’s forest code. Science, 344, 363–364.
- Souza, C., Jr., Siqueira, J., Sales, M., Fonseca, A., Ribeiro, J., Numata, I., . . . Barlow, J. (2013). Ten-year Landsat classification of deforestation and forest degradation in the Brazilian Amazon. Remote Sensing, 5, 5493–5513.
- Steffen, W., Richardson, K., Rockstrom, J., Cornell, S. E., Fetzer, I., Bennett, E. M., et al. (2015). Planetary boundaries: Guiding human development on a changing planet. Science, 347, 1259855.
- Strassburg, B. N., Latawiec, A. E., Barioni, L. G., Nobre, C. A., da Silva, V.P., Valentim, J. F., . . . Assad, E. D. (2014). When enough should be enough: Improving the use of current agricultural lands could meet production demands and spare natural habitats in Brazil. Global Environmental Change, 28, 84–97.
- Taravella, R. (2008). La frontière pionnière Amazonienne aujourd’hui: Projet socio-environnemental de conservation forestière contre dynamique pastorale de deforestation; une analyse stratégique 2000–2006 de l’action collective en “Terra do Meio” (Pará, Brésil) (Doctoral thesis). AgroParisTech.
- Tasker, K. A., & Arima, E. Y. (2016). Fire regimes in Amazonia: The relative roles of policy and precipitation. Anthropocene, 14, 46–57.
- Turner, F. J. (1893). The significance of the frontier in American history. The annual report of the American Historical Society for the year 1893. (pp. 199–222). Retrieved from http://www.archive.org/stream/1893annualreport00ameruoft/1893annualreport00ameruoft_djvu.txt.
- Uhl, C., & Buschbacher, R. (1985). A disturbing synergism between cattle-ranch burning practices and selective tree harvesting in the eastern Amazon. Biotropica, 17(4), 265–268.
- Valverde, O., & Dias, C. V. (1967). A Rodovia Belém-Brasília: Estudo de geografia regional. Rio de Janeiro, Brazil: Instituto Brasileiro de Geografia e Estatística.
- Vasconcelos, S. S., Fearnside, P. M., Graça, P. M. L. A., Nogueira, E. M., de Oliveira, L. C., & Figueiredo, E. O. (2013). Forest fires in southwestern Brazilian Amazonia: Estimates of area and potential carbon emissions. Forest Ecology and Management, 291, 199–208.
- Venturieri, A., Aguiar, A. P. D., Monteiro, A. M. V., Carneiro, A., Alves, D., Câmara, G., . . . Kampel, S. A. (2004). Sumário executivo da missão de campo na região de São Félix do Xingu/Iriri, 13 a 18 de outubro de 2004. Dinâmica de uso e ocupação do território, dinâmica de população e assentamentos humanos e modelagem computacional. Dinâmica territorial da frente de ocupação de São Félix do Xingu-Iriri: Subsídios para o desenho de políticas emergenciais de contenção do desmatamento. Brasília, Brazil: Secretaria de Políticas e Programas de Pesquisa e Desenvolvimento: Rede GEOMA, Ministério da Ciência e Tecnologia. Available at http://www.geoma.lncc.br/Doc_Sumario_Exec_Ministro_Xinguri_Nov2004_Final.doc.
- Vera-Diaz, M. C., Kaufmann, R. K., Nepstad, D. C., & Schlesinger, P. (2008). An interdisciplinary model of soybean yield in the Amazon basin: The climatic, edaphic, and economic determinants. Ecological Economics, 65, 420–431.
- Veríssimo, A., Rolla, A., Vedoveto, M., & Futada, S. M. (Eds.). (2011). Protected areas in the Brazilian Amazon: Challenges and opportunities. Report by Instituto do Homem e Meio Ambiente na Amazônia and Instituto Socioambiental, Belém, Brazil. Available from https://www.socioambiental.org/pt-br/o-isa/publicacoes/protected-areas-in-the-brazililian-amazon-challengs-opportunities.
- Veríssimo, A., Uhl, C., Mattos, M., Brandino, Z., & Vieira, I. (2002). Impactos sociais, econômicos e ecológicos da exploração seletiva de madeiras numa região de fronteira na Amazônia oriental: O caso de Tailândia. In A. C. Barros & A. Veríssimo (Eds.), A expansão madeireira na Amazônia: Impactos e perspectivas para o Desenvolvimento Sustentável no Pará (2d ed., pp. 1–39). Belém, Brazil: IMAZON. Available on http://imazon.org.br/PDFimazon/Portugues/livros/a-expansao-madeireira-na-amazonia-impactos-e.pdf.
- Vitel, C. S. M. N., Carrero, G. C., Cenamo, M. C., Leroy, M., Graça, P. M. L. A., & Fearnside, P. M. (2013). Land-use change modeling in a Brazilian indigenous reserve: Construction a reference scenario for the Suruí REDD project. Human Ecology, 41, 807–826.
- Vitel, C. S. M. N., Fearnside, P. M., & Graça, P. M. L. A. (2009). Análise da inibição do desmatamento pelas áreas protegidas na parte Sudoeste do Arco de desmatamento. In J. C. N. Epiphanio & L. S. Galvão (Eds.), Anais XIV Simpósio Brasileiro de Sensoriamento Remoto, Natal, Brasil 2009 (pp. 6377–6384). São José dos Campos, Brazil: Instituto Nacional de Pesquisas Espaciais (INPE). Available at http://sbsr.dpi.inpe.br/col/dpi.inpe.br/sbsr@80/2008/18.104.22.168/doc/6377-6384.pdf.
- Walker, R., Moore, N. J., Arima, E., Perz, S., Simmons, C., Caldas, M., et al. (2009). Protecting the Amazon with protected areas. PNAS: Proceedings of the National Academy of Sciences of the USA, 106, 10,582‒10,586.
- Walker, R., Moran, E., & Anselin, L. (2000). Deforestation and cattle ranching in the Brazilian Amazon: External capital and household process. World Development, 28, 683–699.
- Walker, R., Perz, S., Caldas, M., & Silva, L. G. T. (2002). Land use and land cover change in forest frontiers: The role of household life cycles. International Regional Science Review, 25, 169–199.
- Weinhold, D., Reis, E. J., & Vale, P. M. (2015). Boom-bust patterns in the Brazilian Amazon. Global Environmental Change, 35, 391–399.
- Wright, S. J., & Muller-Landau, H.C. (2006). The future of tropical species. Biotropica, 38, 287–301. Retrieved from http://www.jstor.org/stable/30044025.
- Wunder, S., Börner, J., Tito, M. R., & Pereira, L. (2009). Pagamentos por serviços ambientais perspectivas para a Amazônia legal (2ª ed.). Série Estudos 10, Brasília, Brazil: Ministério do Meio Ambiente. Retrieved from http://www.mma.gov.br/estruturas/168/_publicacao/168_publicacao17062009123349.pdf.
- Yanai, A. M., Fearnside, P. M., Graça, P. M. L. A., & Nogueira, E. M. (2012). Avoided deforestation in Brazilian Amazonia: Simulating the effect of the Juma sustainable development reserve. Forest Ecology and Management, 282, 78–91.
- Yanai, A. M., Nogueira, E. M., Graça, P. M. L. A., & Fearnside, P. M. (2017). Deforestation and carbon-stock loss in Brazil’s Amazonian settlements. Environmental Management, 59, 393–409.
- Zarin, D. J., Harris, N. L., Baccini, A., Aksenov, D., Hansen, M. C., Azevedo-Ramos, C., . . . Loboda, S. (2016). Can carbon emissions from tropical deforestation drop by 50% in five years?. Global Change Biology, 22, 1336–1347.