Open Access
Translator Disclaimer
22 June 2022 Impact of Productive Activities on Forest Cover Change in the Calakmul Biosphere Reserve Region: Evidence and Research Gaps
Jovanka Špirić, Mariana Vallejo, M. Isabel Ramírez
Author Affiliations +

Background and Research Aims: Human activities seeking to satisfy various needs have resulted in deforestation and other forest cover change processes. The Natural Protected Areas are among the most efficient instruments to contain forest loss. The compensation from conservation is not sufficient to compete with land uses with higher economic rent, such as timber extraction and food production. This study summarizes the evidence and identifies research gaps on forest processes caused by productive activities in Mexico's Calakmul Biosphere Reserve.

Methods: We systematically reviewed the scientific literature investigating forest processes caused by the productive activities in the Calakmul, including the transition zone. We calculated the frequencies of codes on forest processes and productive activities in the entire sample (53), evaluated each code's significance in the qualitative synthesis and interpretation, and summarized the measurements of forest processes considering only the primary studies (46).

Results: Deforestation was the most commonly investigated process. Traditional agriculture initially caused deforestation, while livestock and conventional agriculture became more dominant recently with the agricultural intensification policies. Few articles investigated forest degradation experiencing a steady increase from fallow shortening and selective logging. Also, few studies identified forest recovery resulting from long fallows and core zone delimitation. No publications evaluated the forest cover impact of sustainable initiatives.

Conclusion: The tendency to quantify deforestation on a regional scale masks presence of other forest processes. The rural development programs in Calakmul did not include the environmental perspective, while participation in sustainable initiatives was low. The understanding of productive activities at the local level will allow differentiation of the long-term from temporary forest dynamic.

Implications for Conservation: To assure resilient and inclusive growth in Calakmul, the reduced-impact logging, sustainable agricultural intensification, improved fallows, and beekeeping should be supported with monetary resources that cover the transaction costs of unsustainable livestock breeding and industrial agriculture.


Throughout history, human activities seeking to satisfy various needs have resulted in deforestation and other forest cover change processes (Williams, 2006). A historically exceptional rapid and extensive forest clearing occurred between 1950 and 1980 (Ramankutty et al., 2010). In the 1990s, the annual rate of global deforestation started to slow down, from 7.84 million ha in 1990–2000 to 4.74 million ha in 2010–2020 (FAO, 2020a). Nevertheless, recent global estimates suggest that forest degradation (no change in land use) emits 40%–212% more carbon dioxide than deforestation (Baccini et al., 2017; Pearson et al., 2017). Currently, forest degradation is more widespread than deforestation in tropical regions (Trondoli et al., 2020) and contributes to one-fourth of the total forestry sector emissions (Griscom et al., 2009; Pearson et al., 2017).

Given the urgency to reach at least net-zero CO2 emissions to limit the rapid and intense global climate change and its adverse effects, we must consider regional modulations for planning adaptation strategies (IPCC, 2021). As a response, 141 countries, including Mexico, signed the Declaration on Forest and Land Use in 2021 as the culmination of a chain of efforts from global environmental governance. This declaration urges humanity to limit climate change, achieve resilient and inclusive growth, and stop and reverse forest loss and land degradation through a sustainable land use transition (UNFCCC, 2002). This change may propel human activities that result in positive examples of forest cover change processes, such as forest succession and recovery (Keenan et al., 2015; Lambin & Meyfroidt, 2011).

In Mexico, the forest area decreased from 70 million ha in 1990 to 65 million ha in 2020 (FAO, 2020a). The direct cause of forest loss in 88% of cases was the expansion of both rainfed agriculture for subsistence and intensive commercial agriculture (GFW, 2020). Recent studies suggest that the annual net forest loss has decreased from −0.32% (1990–2000) to −0.19% (2010–2020) (FAO, 2020a). From 2001 to 2013, 392,920.49 ha of forest were lost in the state of Campeche to livestock breeding (59%) and mechanized agriculture (30%) for the most part, which represents an annual net deforestation rate of −0.39% (Ellis et al., 2015). However, the forest degradation rate has not been evaluated with precision yet, and the evaluations reported to the FAO range from 22,800 to 300,000 ha/year (2000–2015) (CONAFOR, 2020; Madrid, 2020). In Mexico, the land extension affected by forest degradation was more significant than the affected by deforestation in the last decades (CONAFOR, 2017a).

The establishment of Natural Protected Areas (NPAs) has been one of the most efficient instruments to reverse the forest loss and contain the advance of the agricultural frontiers (Humphreys, 2006). However, the pressure against protected forests remains strong because the economic compensation from forest conservation or sustainable productive initiatives is not sufficient to compete with land uses with higher economic rent, such as wood extraction, food, fodder, and biofuels production, and mining (Bezaury-Creel & Gutiérrez Carbonell, 2009; Fitzherbert et al., 2008; Ramírez et al., 2015). Therefore, we need to continue analyzing the productive activities, and their impacts on the forest cover change processes in the NPAs and promote local sustainable practices.

There are currently 183 federal NPAs in Mexico, including 42 with the category of Biosphere Reserve (BR) (CONANP, 2022), a model proposed by the United Nations Educational, Scientific, and Cultural Organization's Man and Biosphere Program (UNESCO MAB). BRs are natural areas of international importance due to their biological and cultural diversity and the potential to implement sustainable rural development initiatives within them (UNESCO, 2017). Each BR has three zones: core, buffer, and transition (Bridgewater, 2016; UNESCO, 1996). Core zones are dedicated to conservation, and only selected non-destructive and low-impact research and education activities are allowed. Buffer zones surround or adjoin the core areas. Their primary function is to host the development and exploration of cooperative and ecologically sound activities, such as ecotourism, recreation, and basic research. Finally, transition zones are spaces between the BRs and the surrounding areas where the local population may develop sustainable productive activities. The outer limits of the transition area are not legally determined. Still, they can be defined by natural phenomena (forest edges, rivers, lakes, etc.) or by human-made forms (roads, railroads, borders, etc.) (UNESCO, 2021). In the Mexican model of BR, the legally determined buffer zone includes the activities allowed in the transition zone (Halffter, 1984).

We selected the Calakmul Biosphere Reserve (CBR) as our study area, which is administratively located within the boundaries of the state of Campeche in the Yucatan Peninsula in southeastern Mexico. Since its establishment in 1989, the CBR has attracted many conservation and development projects and numerous research groups, resulting in multiple publications. However, only one review article has been published that analyzes primary research publications about deforestation caused in the last 50 years in the entire Yucatan Peninsula (Ellis, Hernandez Gomez, & Romero-Montero, 2017).

Therefore, a literature review is necessary given Mexico's adoption of the Reducing Emission from Deforestation and forest Degradation, plus promoting conservation, sustainable management of forests, and enhancement of forest carbon stocks (REDD+) (CONAFOR, 2017b). REDD+ is an international forest and climate change policy designed to financially reward reduction in land use based emissions through carbon markets or conventional financial aid (UNFCCC, 2010). Despite the critique of its technical complexity, economic inefficiency, and potential negative social and environmental impacts on local indigenous people (e.g., Bayrak & Marafa, 2016; Osborne et al., 2014), REDD+ is being implemented in many developing countries under different policy design.

REDD+ in Mexico is planned as a set of productive and conservation activities from forestry and agriculture to promote sustainable rural development. It implies the improvement of social welfare and economic activities while guaranteeing natural resources conservation within territorial units defined by environmental boundaries (e.g., hydrological basins, biological corridors) (CONAFOR, 2017b). Therefore, CBR, including its broader transition zone, was included as one of the priority areas for the early REDD+ activities (ATREDD+) (2010–2015) (CONAFOR, 2015).

To summarize the evidence of forest cover change processes caused by productive activities in the study area, clarify controversies, and identify learnings and research gaps, we systematically reviewed the existing publications (sensu Haddaway et al., 2015). We asked the following question: Which positive and negative forest cover change processes caused by productive activities have been identified, described, and evaluated in the Calakmul Biosphere Reserve and its transition zone?


Study area

The Calakmul Biosphere Reserve in the southeastern state of Campeche is the largest forested area in the Yucatan Peninsula (722,000 ha). CBR is part of the Maya Forest, that is the second-largest neotropical forest after Amazonia spanning southern Mexico, Belize, and Guatemala, and a biodiversity and deforestation hotspot. In addition, CBR is part of the Mesoamerican Biological Corridor, which is the largest bioregional conservation initiative in Central America (Eaton & Lawrence, 2009).

CBR's core and buffer zones are mainly located in the municipality of Calakmul. Its transition area spreads to the adjacent municipalities both in the states of Campeche and Quintana Roo. However, we focus only on the broader CBR area in Campeche, which includes the municipalities of Hopelchén, Escárcega, Candelaria, and Champotón (Figure 1). This is because different development, agricultural, and forestry policies are implemented at the state level in Mexico (CONAFOR, 2017a). In addition, the five selected municipalities have had the highest forest loss to agriculture in the state of Campeche from 2001 to 2013 (Ellis et al., 2015).

Figure 1.

Study area: transition zone of the Calakmul Biosphere Reserve, including limits of the municipalities of Hopelchén, Escárcega, Candelaria, and Champotón neighboring the municipality of Calakmul where the core and buffer zone of CBR lay.


The dominant land tenure in the region is the ejido—a type of social land ownership unit gained in the 1910s Mexican Peasant Revolution when the nation granted customary rights to landless farmers to meet their subsistence needs (García-Barrios et al., 2009). Usually, one part of the ejido land is managed in common (mostly forests), while the rest is divided between the ejido members (ejidatarios) and is used for agriculture. In most cases, the ejidatarios have to work the parceled lands to keep their land rights, which they can transfer only to one of their descendants (Ley Agraria, 2018). The CBR core area is within the territories of ejidos; however, it is managed by the National Commission of Protected Areas (CONANP). Some private lands are located predominantly in buffer and transition CBR zones (Klepeis, 2003).

The total study area, including the five selected municipalities, is 3,747,585 ha, and it is inhabited by 293,640 people, 70% of whom live in poverty (CONEVAL, 2020; INAFED, 2022; INEGI, 2020). The dominant ethnic groups in the study area are the Yucatec Maya, Chol, Tzeltal, Tzotzil, and Chontal indigenous people, along with the mestizo population (both indigenous and Spanish ancestry) that migrated to the study area from the Mexican states of Chiapas, Tabasco, Veracruz, Oaxaca, and Michoacan (Alonso Velasco, 2020). In addition, there are Mennonites (a religious group of industrial farmers of European descent) that immigrated to the study area from the states of Durango, Chihuahua, Zacatecas, and Tamaulipas (Ellis, Romero Montero, et al., 2017; Roy Chowdhury & Turner II, 2006; Porter-Bolland et al., 2007).

The climate is sub-humid warm tropical, with a mean annual temperature of 25°C and marked by dry and rainy seasons with hurricanes (Eaton & Lawrence, 2009; Porter-Bolland et al., 2007). The topography is karst with underground drainage and no superficial flows. The dominant soil type is rendzina, whose main characteristic is low fertility. Our study area hosts different tropical forests, including the low deciduous and sub-evergreen forest, the medium sub-deciduous and sub-evergreen forest, the high sub-evergreen forest, and various associations of hydrophytes (Geoghegan et al., 2010).

The forest ecosystems are rich in precious timber and melliferous species that have historically favored beekeeping and forest management for timber production (Porter-Bolland et al., 2007). The landscape is composed of mature forests (montañas), secondary forests in different stages of succession (acahuales), and agricultural areas that include shifting agriculture, livestock, and mechanized agriculture (Krylov et al., 2018; Porter-Bolland et al., 2007). In addition, the numerous and well-preserved archeological sites with Mayan ruins host many cultural and ecotourism activities. In 2014, CBR became a Mixed World Heritage (UNESCO, 2014).

Articles selection

We consider local productive activities as those of the primary economic sector involved in the extraction and production of natural resources for subsistence or commercial purposes, such as agriculture, livestock breeding, beekeeping, and forestry (Pérez & Merino, 2016). Productive activities are the direct human causes of forest cover changes and their underlying factors. They act as demographic and economic stressors (e.g., globalization and market liberalization) and the accompanying mounting demand for food (crops and livestock) and energy (oil crops, fossil fuel extraction, and mining), and the resulting public policies (Lambin et al., 2003). Our review method follows systematic review principles, such as systematic searching, screening, and critical appraisal, which increase transparency, objectivity, replicability, and reliability (Haddaway et al., 2015, 2020).

First, we tested our review question by evaluating the presence of main PICo elements (P—Problem or Population affected; I—a phenomenon of Interest, Intervention, or exposure; and Co—Context, geographical, economic, political, or biological) (Haddaway et al., 2015). Our P stands for positive and negative impacts on forest cover (see Table 1 for a definition of each process). Our I represents productive activities from the primary economic sector that are supported by governmental, non-governmental, or private actors (see Table 2 for a definition of each activity). Finally, our Co is CBR, our geographic study area. After assuring our question is researchable through a review, we wrote the review protocol and generated a search string.

Table 1.

Definition of forest cover change processes considered in the review.


Table 2.

Definition of selected productive activities present in our study area.


The search string is composed of a combination of terms corresponding to each of the PICo elements and their synonyms: (deforestation OR “forest degradation” OR “forest loss” OR “land$use change” OR “forest transition” OR “forest disturbance” OR “forest restoration” OR regrowth OR revegetation OR reforestation OR “forest recovery” OR “forest fragmentation” OR “forest succession”) AND (activities OR agriculture OR livestock OR cattle OR harvesting OR logging OR management OR beekeeping OR apiculture OR pasture OR milpa OR agroforest* OR silvopastoral OR agrosilvopastoral OR orchard OR plantation OR cultivation) AND (Calakmul OR Campeche OR Yucatan). We performed our search in English in April 2021 and found 190 (Web of Science-WoS) and 158 (Scopus) scientific publications. We translated the string into Spanish and used it in the Scielo academic database, finding 98 publications. We screened all search results to determine whether or not a publication was relevant to the review. At this point, we applied no time or document type restrictions. However, the selection of search databases limited our sample to academic publications, excluding gray literature, such as reports and thesis. In addition, we only considered documents in English and Spanish.

We then evaluated publications for inclusion at three successive levels. First, we assessed them by title. We selected 149 publications after checking their titles and excluding duplicates. Then, we evaluated the abstract of each publication that was potentially relevant based on the title. This procedure reduced the number to 74 publications that we analyzed in total. The final sample included only those studies that complied with the following three criteria: (1) they investigate variables for identification and/or quantification of forest cover change processes, such as land cover and change, carbon stocks, emissions, and biomass, (2) they do so concerning the activities of extraction and production of raw materials for subsistence or commercialization, and (3) they focus on the broad transition area of the CBR within the borders of the state of Campeche.

Relevant articles included qualitative and quantitative studies of forest conditions relating to productive activities considered as causes of positive or negative changes. They provided original data or referred to other studies containing supplementary information. The studies citing other primary field studies helped to check the comprehensiveness of our sample. Due to the focus on forest cover change as a proxy measure of carbon emissions from the forestry sector, we did not take into account ecological studies evaluating the impact of productive activities on other ecosystem services, such as forest structure and composition, invasive species, biodiversity, nutrients, or biomass in soil, microclimate and water flow regulation. Furthermore, we did not consider the environmental history studies that investigated periods before the 20th century or those evaluating the governance of CBR.

On the other hand, we included all the studies that investigate our study area even when performed at a different scale of analysis, for example, studies comparing CBR and other national or international case studies. We discarded 21 publications during the full-text revision phase (see  Appendix 1). Our final sample counts 53 publications, including 51 journal articles and two book chapters. These were written by 31 different first authors and published in 33 journals and one book (see  Appendix 2 for the final sample metadata).

Data analysis

We used a coding technique in MaxQDA software to organize and extract data. We assigned the predetermined codes based on the review question elements to specific units of analysis (paragraphs, sentences, or words) (Saldana, 2015). We organized our list of codes in two general categories: (1) forest cover change process (listed in Table 1), including terms, definitions, and numerical or qualitative measurements; (2) productive activities (listed in Table 2), including socio-economic, ecological, cultural or political reasons to adopt/increase or quit/decrease them, as well as related practices (specific actions used by local actors in the production process, e.g., fallowing) and policies (programs, projects, and initiatives promoted by government or other actors). Both practices and policies were coded as positive or negative depending on how the authors identified them: either as avoiding/decreasing or causing/increasing deforestation and/or forest degradation.

The coding technique organized the data and allowed its interpretation. An important step in the qualitative content analysis was calculating the code frequencies to identify their prevalence. Additionally, we evaluated the significance of each code in the qualitative interpretation analysis, which allowed us to ponder, organize, connect, and synthesize the results from different studies (Saldana, 2015). We calculated the relative frequency distribution of assigned codes to evaluate their relative representation in the entire sample. Finally, we calculated the frequency of study focus and performed qualitative synthesis and interpretation, focusing only on the primary studies (46) (Grant & Booth, 2009) (primary and secondary studies are marked with * and ** in the References list, respectively).

We used the segments containing numerical data about measurements of forest cover processes from primary studies to construct a summary table ( Appendix 3). The studies using quantitative criteria and indicators to measure the forest processes did so at different geographical and temporal scales, which does not allow for generalization or calculation of the rates for the entire study area. However, we observed some general trends in forest cover change processes attributable to each productive activity from the results of primary studies.

We grouped and extracted segments containing textual data assigned with the same code in specific documents that we used to construct the narrative synthesis (Grant & Booth, 2009). We organized the synthesis around the productive activities and policies and grouped them based on their impact on forest cover (deforestation, forest degradation, forest recovery and transition, and forest conservation). We critically appraised the methodological rigor of each primary research article during the information interpretation process.


Relative frequency distribution of codes

The code frequency (78%) shows that data concerning negative forest cover change processes were dominant in our sample (Figure 2). When looked at separately, the most frequently mentioned negative changes were deforestation (45%) and forest loss (10%), both of which represent the same process. Although forest degradation is the third most frequently mentioned process, it has only 6% of the codes assigned. The reason may be that degradation is more difficult to observe and measure than deforestation. Conversely, the information on positive processes was less frequent (only 22% of the assigned codes), which indicates their occurrence in the region. The most frequently mentioned positive changes were forest succession and recovery, which represent the same process related to traditional fallowing, agricultural abandonment, and productive reconversion to agroforestry.

Figure 2.

Frequency of codes on positive (dark gray) and negative (light grey) forest cover change processes.


Analyzing the frequency of codes assigned to practices associated with each activity, traditional agriculture, big livestock breeding, and forest harvesting (51%, 24.5%, and 10%, respectively) were associated with negative forest cover changes. However, forest harvesting was also the most frequently related to positive forest cover changes (53%). Forest harvesting does not include the total removal of the forest or the land-use change, and forest authorities regulate it. In addition, public policies implemented in the study area caused adverse effects on traditional agriculture and big livestock. However, some public policies promoting traditional agriculture, agroforestry, and beekeeping were factors of positive changes in forest cover also (Figure 3). The following section will discuss in further detail the relation between productive practices and policies and forest cover change processes.

Figure 3.

Frequency of codes on positive and negative practices and policies concerning productive activities.


Frequency of primary study focus

Among the studies with primary data (46), deforestation was the most investigated process (11), with commercial agriculture and cattle ranching as their primary concern (Table 3 and  Appendix 4). Deforestation was referred to with various terms, including forest loss, clearance, conversion, and land-use change. Only five articles investigated forest degradation caused by shifting cultivation and forest harvesting in CBR. As for the positive forest cover change processes, most articles (5) investigated passive forest recovery, including forest succession and regeneration. An important number of investigations (12) focused on several negative and positive processes associated with a selected group of productive activities presented in the area.

Table 3.

Number of primary studies investigating negative and positive forest cover change processes in relation to productive activities (the intensity of gray shades corresponds to the number of articles).


A narrative synthesis of qualitative data

Negative forest cover change processes

Most primary studies in our sample investigated individual negative forest cover change processes concerning productive activities (26), while an additional twelve did so by grouping them with positive processes.


Although traditional agriculture establishment was the main deforestation driver in the first period, big livestock breeding and conventional agriculture were the leading causes of deforestation within the study area in the more recent periods (Table 4).

Table 4.

Primary studies' results on land-cover and land-use changes recognized as deforestation resulting from the establishment and expansion of productive activities (e.g., pasture, traditional crops, commercial crops, bare land).


The process of pasture expansion starts with forest clearance; it is then followed by land use for traditional agriculture for a few years to finally end with seeding pasture (Porter-Bolland et al., 2008; Busch & Geoghegan, 2010). Since pasture is its final use, even those areas considered unsuitable for milpa, such as lowland flooded forests, have now been deforested (Porter-Bolland et al., 2008). The milpa and the areas under irrigated agriculture were transformed into the pasture, for example, rice fields supported by governmental agricultural mechanization programs in the 1970s were abandoned in the 1980s due to weed invasion, disease, and inadequate water control (Porter-Bolland et al., 2008). Pastures have experienced a steady increase since they were introduced through governmental policies, despite the limitations such as soil type, water scarcity, and distance to market centers (Busch & Vance, 2011).

Livestock development in the area does not follow an idealized, long-term development logic of a yearly increase in pasture areas and cattle. Due to the cash and labor constraints, farmers build pasture and ranching infrastructure (e.g., fences, artificial ponds) over several years, often without owning livestock (Busch & Vance, 2011). In addition, the fact that producers sell cattle does not necessarily mean that their farms have reached a minimum level of operational development but may only indicate that they need emergency money. The studies concur that raising cattle also fulfills a security function as a wealth accumulation and savings strategy (Busch & Geoghegan, 2010; Schmook & Vance, 2009).

Despite these shortcomings and barriers, and the fact that pasture brings a relatively modest return to the household economy, extensive livestock farming provides the highest profit per day of labor invested, and it is considered an economically beneficial alternative by small producers (Busch & Geoghegan, 2010; Busch & Vance, 2011). Pasture maintenance requires less labor (in smaller areas), and it is less vulnerable to soil infertility and climate extremes than maize and jalapeño chili peppers. In other words, cattle are more likely to survive hurricanes and, unlike irrigating crops, can be brought water in case of droughts (Busch & Geoghegan, 2010; Busch & Vance, 2011). Another reason for pasture increase may be that it maintenance is considered a relatively cheap way to keep the land under production as required by agricultural programs (Schmook & Vance, 2009).

Pasture can be grown almost permanently if properly maintained and under a moderate stocking rate. However, bracken fern (Pteridium aquilinum) invaded large sites of former pastures in the Calakmul municipality (Roy Chowdhury, 2006; Reyes-Hernández et al., 2003; Schmook & Radel, 2008; Schmook et al., 2011; Turner et al., 2001; Vester et al., 2007). This process proves the potential reversibility of pasture thanks to its abandonment or improper management in some cases. Additionally, given that it was not economically viable for local farmers to reestablish pasture in areas invaded by bracken fern, new forest areas were open for livestock production, contributing to the overall deforestation of the area (Busch & Geoghegan, 2010; Turner et al., 2016).

Owning pasture for renting or animal production and sale increased the farmers' economic capacity to open additional forest areas for agricultural use. Furthermore, cattle ranching freed up labor for other income-generating activities, such as migration. In turn, the remittances allowed for the enlargement of pasture areas despite the outflow of people, following a hollow frontier pathway (Busch & Vance, 2011; Radel, Schmook, & Chowdhury, 2010). Market closeness, larger land area, higher average rainfall, government subsidies, farmer's education level, and greater wealth increased pasture adoption. Greater wealth is related to the sum of years that the household had grown jalapeño chili peppers (Capsicum annuum L.) and to the migration status of the male household head (Busch & Geoghegan, 2010; Roy Chowdhury et al., 2006; Radel, Schmook, & McCandless, 2010).

Chili producers earned more money than most other farmers, allowing them to use more land (Busch & Vance, 2011). According to Keys (2010), chili was the most crucial income generator for the majority (85%) of the region's farmers in 2000. Chili holds second place after the milpa in the area devoted to it. Chili production in the southern CBR (municipality of Calakmul) takes two forms—swidden (70% of farmers), which is similar to the milpa cycle, and mechanized (30%). Mechanized plots are less likely to be converted back into the forests. Those farmers with mechanized land tend to cultivate more land, while those without it expressed a desire to mechanize their land. However, chili production demands a large amount of labor and external inputs of agrochemicals (both fertilizers and pesticides). This crop requirement is why farmers cleared primary, old-growth forests with high soil nutrient content to cultivate jalapeño chili. Chili was, therefore, a significant deforestation factor mainly in the first period of its establishment (1987–1992). However, in the subsequent period (1992–1997), chili production did not significantly impact deforestation, probably because the ejidos with the largest deforested area had to direct their efforts toward their mechanization to produce enough to pay back government credits (Reyes-Hernández et al., 2003).

In Hopelchén in the 1980s, the government-supported mechanized agriculture for commercial crops (maize, soy, and sorghum) was performed mainly by the experienced Mennonites migrants. They were expected to teach modern agriculture to Maya communities. Ejidos progressively adopted agricultural mechanization and currently either cultivate their land or rent it to Mennonites (Ellis, Romero Montero, et al., 2017). This replacement of traditional milpa with permanent mechanized plots contributed to the deforestation in the municipality (1986–2015). In addition, contamination from agrochemicals and pollen of genetically modified crops used in mechanized commercial agriculture has negatively affected local honey production.

Forest degradation

The shifting cultivation, agricultural use of fire, and selective logging were the productive activities that caused forest degradation and whose impact has steadily increased over the investigated period (see Table 5).

Table 5.

Primary studies' results on land-cover and land-use changes recognized as forest degradation resulting from the maintenance of productive activities (e.g., secondary forest, secondary growth, burnt areas, bracken fern).


The shifting cultivation cycle typically involves a few years of clear-cut and burned forest land use followed by fallow periods characterized by natural regeneration of the secondary forest. However, currently, the shifting cultivation cycle in the Yucatan Peninsula includes shorter fallow periods (6–11 years), which prevents full recovery of aboveground and soil carbon stocks (less than 66% of mature forest stocks) (Eaton & Lawrence, 2009). Shorter fallows keep the biological wealth of forest permanently diminished, including the propagation of invasive species, such as sunflower goldeneye (Viguiera dentata), locally known as tajonal (Keys, 2010). However, the mean combined carbon stock tends to be larger in young and old secondary forests (only 22% of the old forest stocks), while it is the lowest in middle-aged secondary forests. This difference in carbon stock is because of the decline of soil organic carbon during the first 5–10 years of regrowth, followed by an increase (Eaton & Lawrence, 2009). However, those ejidatarios who practice longer fallow hold more agricultural areas, supplying resting sites by opening new ones each year.

Besides forest age, the number of cultivation-fallow cycles negatively affected the aboveground biomass carbon stocks, experiencing a decrease of approximately 64% from one to four cycles (Eaton & Lawrence, 2009). Each cultivation cycle begins with cutting and burning secondary forests to remove residual biomass and enrich the soil. Therefore, it is not surprising that the most significant number of fire hot spots occurred in secondary fallow forests, followed by pasture, and milpas, where farmers deliberately initiate fires that sometimes last several days (Cheng et al., 2013). The fire danger index was “medium-low” to ”high” for most of our study area. Although a more extended perimeter of agricultural areas increases fire risk in the neighboring fire-sensitive medium tropical forests, the hurricanes reach them with reduced strength, resulting in fewer forest fuels (Rodríguez-Trejo et al., 2011). However, fallen dead trees can be a source of local income through charcoal production, a fire prevention measure (Schramski & Keys, 2013).

The precious wood species, in particular mahogany (Swietenia macrophyla King) and cedar (Cedrela odorata L.) (Klepeis, 2003), were depleted in the extractive forest concessions during the first half of the 20th century. As a result, some authors no longer considered timber harvesting a primary livelihood strategy. Most forest ejidos in the study areas hold government permits to harvest timber of lesser-known species such as chacáh (Bursera simaruba (L.) Sarg.) and granadillo (Platymiscum yucatanum) (Porter-Bolland et al., 2007). Selective logging, or the removal of commercially valuable trees, is a dominant timber harvesting practice in the Yucatan Peninsula. However, some carbon emissions (37%) originate from felling, skidding, and construction of log landings and logging roads (Ellis et al., 2019).

Although the impact of selective logging on carbon emission rates in the investigated area is low compared to other regions of the world, implementing reduced-impact logging (RIL) practices could still reduce it even further. These practices include directional felling, planning of logging and skid trails, mapping and marking of harvested trees, pre-cutting of lianas and vines, and the use of modified tree farmer tractors. However, even when the investigated ejidos in our study area had low logging intensity, they did not implement the RIL practices and, therefore, had high carbon impacts. Only one ejido implemented the RIL practices as part of the Forest Stewardship Council (FSC) forest certification process (Ellis et al., 2019). Although several actors promoted certification, including the Rainforest Alliance, CONAFOR, The Nature Conservancy (TNC), and United Nations Development Program (UNDP), only those ejidos with larger harvest volumes and better-managed operations could afford it. Community Forestry Management (CFM) helps overcome the lack of direct access to timber and non-timber forest products' market, local and inter-ejido conflicts, and the need to carry out logging activities without a formal management plan (Armenta-Montero et al., 2020). However, there is a lack of government support for CFM. In other words, since 2010, REDD+ has been a central forest policy in Mexico, and it focuses principally on payment for ecosystem services.

Positive forest cover change processes

Eight primary studies in our sample investigate positive forest cover change processes concerning productive activities, while only four measured related land-cover and land-use changes (Table 6). Many others only mention the need to promote these activities in the region.

Table 6.

Primary studies' results on land-cover and land-use changes recognized as forest succession and recovery (e.g., regrowth, older secondary forest, increase of mature forest) resulting from the abandonment of productive activities.


Forest recovery and transition

Shifting cultivation can be considered a biodiversity-friendly agricultural system, but only if long fallows come after short cultivation periods to allow secondary forest regeneration from accumulated tree seeds. Secondary forests are important carbon stocks, and trees in the early stages of succession capture and store a significant amount of carbon. The secondary succession of tropical forests varies depending on the biophysical conditions and the disturbance that initially caused the forest loss. In our study area, it takes between 12 and 25 years after the abandonment of agriculture to recover half of the biomass of mature forests and 35 years to recover nearly 85% of the basal area of mature forests (Read & Lawrence, 2003). According to Turner et al. (2001), a forest takes between 25 and 30 years to reach its maturity again. Fully recovering carbon stocks takes approximately 85 years, while regaining biomass levels before first cultivation would take more than 125 years (Aryal et al., 2014). However, shorter or interrupted traditional agriculture cycles do not allow forest carbon stocks to recover completely. Furthermore, while some areas are cleared for pastures and agriculture, others are left or abandoned, allowing secondary succession. Some studies suggest that the southern part of the study area (in the municipality of Calakmul) shows the characteristics of an initial stage of forest transition because the recovery of secondary forest from cropland occurred in large areas (Busch & Geoghegan, 2010; Roy Chowdhury, 2010; Schmook & Radel, 2008). These studies assume that increasing revenues from commercial crops and cattle ranching provoked the outflow of people through international work migration.

Forest conservation

CFM, Mayan Community Forest Reserves, beekeeping, and agroforestry systems are productive activities that propitiate the conservation of forests (Casey & Caviglia, 2000; Levy-Tacher et al., 2019; Porter-Bolland et al., 2015). Timber harvesting with CFM, including local norms and traditional practice, preserved 80% of forest cover in an ecological state similar to an unmanaged forest and reported more tree species (Levy-Tacher et al., 2019). CFM also ensured the connectivity of the forest landscape. During the first half of the 20th century, the extraction of chewing gum resin from chicle trees (Manilkara zapota L.), a non-timber forest product, was an economically significant activity that favored forest conservation in the study area (Abizaid & Coomes, 2004). Mayan Community Forest Reserves provide firewood, fruits, and construction material to local people and nectar to the bees; they also regulate microclimates and protect from fire and hurricanes (Levy-Tacher et al., 2019).

Beekeeping with honeybees of the genus Apis was adopted in the 1970s by traditional Maya beekeepers and is another low-intensity productive activity (Porter-Bolland et al., 2008; Rodríguez-Solorzano, 2014). As a result, government and non-governmental organizations (NGOs) promoted apiculture, which currently represents one of the primary sources of income for communities, including honey exportation. In addition, agroforestry systems in the study area that are part of the Maya tradition combine fruit, forage, and medicinal plants and trees and have received strong support from NGOs (Casey & Caviglia, 2000).

Policies and actors

The spatial and temporal forests cover dynamic responds to the social processes and public policy presented in the study area. However, only a few primary studies measure the impacts of policies and actors on forest cover change processes. In contrast, many others only recognized policies and actors as important factors that promoted particular land uses in the region (Table 7).

Table 7.

Productive activities, their impacts on forests, promoting actors and policies, and reversibility measures suggested in the reviewed articles.


Agriculture programs

With chicle extraction being no longer profitable after World War II and the rapid exploitation of marketable precious wood species in the 1980s that led to the decline in forestry activity, the Mexican government moved rapidly to target the region for agricultural development (Klepeis, 2003). Since the 1970s, the deforestation of the primary forest has occurred under state-promoted policies (see Table 4). These included colonization policies (construction of highway, the extension of ejido land grants, and the sale of state-owned land to Mennonites) and commercial agriculture and livestock production programs to exploit resources for macroeconomic development under the North American Free Trade Agreement (NAFTA) and to provide small farmers with subsistence (Krylov et al., 2018). The National Deforestation Program (PRONADE) provided credit to smallholders who cleared upland forests to establish pasture and cropland (Klepeis, 2003; Velasco & Torres, 2019).

In 1975, three independent producers initiated chili production in one village. This activity spread rapidly to other communities through the market intermediaries (Keys, 2010). The National Solidarity Program (PRONASOL) “Crédito a la Palabra,” supported the production of the jalapeño chili for commercialization among small producers (2–3 ha) (Reyes-Hernández et al., 2003). The funds of the Program of Direct Support to the Countryside (PROCAMPO) were available to large and small farmers (min. 1 ha) that cultivated on the same plot of land maize and other staple crops, such as beans, wheat, soybeans, sorghum, rice, and cotton. PROCAMPO's primary aim was the sedentarization of swidden agriculture and the intensification of commercial crops (Roy Chowdhury et al., 2006). Since 1995, PROCAMPO has included finance for establishing pastures, acquiring rural equipment and development, and procuring agricultural mechanization. The farmers' credits (“Alianza para el campo” program) and subsidies for equipment helped overcome startup costs, which incentivized the establishment of pasture in anticipation of future government subsidies for cattle ranching (Reyes-Hernández et al., 2003).

Both PROCAMPO and Alianza were positively associated with increased, cultivated areas of mainly pasture. In the municipality of Calakmul, PROCAMPO directly caused forest area loss as a consequence of the compensation that local producers made for removing the cultivated plots from the swidden agriculture cycle (Díaz Gallegos et al., 2001; Schmook & Vance, 2009). Reyes-Hernández et al. (2003) suggested that the ejidatarios that received more funding from PROCAMPO caused less deforestation because they used this money to cover their basic needs. This program did not influence deforestation in neighboring Hopelchén. Two studies coincide that the Alianza program was not associated with further deforestation. This program included technical assistance, a flexible design, specific activities, and land area selection; it also provided nonmonetary support (equipment and seeds).

Agroforestry, agroecology, and other sustainable activities

Some NGOs promoted the establishment of agroforestry parcels (e.g., Pimenta dioica—allspice), agroecological demonstration plots, and organic farming as alternatives to commercial crop production principally in the Calakmul municipality (Casey & Caviglia, 2000; Chowdhury, 2007; Roy Chowdhury et al., 2006). However, the above-mentioned sustainable initiatives failed to recruit farmers except for the introduction of velvet bean (Mucuna pruriens L.), a nitrogen-fixing legume, and the productive reforestation of secondary forests because they considered other sustainable activities as risky as chili cultivation (Keys, 2010). Other programs promoted agricultural intensification by subsidizing the use of tractors, as well as non-forest-extractive land uses like organic beekeeping and ecotourism. However, none of the identified studies investigated the impact of these sustainable initiatives on forest cover.

Conservation and forest policies

Some authors suggested that the establishment of CBR led to an increase in deforestation in the newly established ejidos because of their need to assure claim over the land (Abizaid & Coomes, 2004; Reyes-Hernández et al., 2003; Rueda, 2010). However, others demonstrated that the biosphere reserve slowed deforestation rates in the study area (Klepeis, 2003; Neeti et al., 2012; Vester et al., 2007) (Table 4) and even provoked an increase in the forest recovery area after 1989 (Roy Chowdhury, 2006) (Table 6). As mentioned previously, REDD+ is the central forest policy in Mexico, and it combines forestry and agricultural activities for sustainable rural development. Since 2010, REDD+ has been implemented in the Yucatan Peninsula by the forest owners (predominantly ejidos) through the government forestry programs and international NGO pilot projects (e.g., Alianza MREDD+).

Ellis, Sierra-Huelsz, et al. (2020) found that the REDD+ interventions were the most effective in reducing deforestation in those municipalities and communities where timber harvesting was combined with traditional agriculture for subsistence. The ejidos that perform livestock breeding as their dominant activity or combine it with mechanized agriculture for commercial crops and forestry harvesting had the lowest REDD+ effectiveness. Those predominantly cattle ranching municipalities in the southern part of our study areas (Calakmul and Candelaria) that share a border with Belize and Guatemala are also experiencing illicit logging, drug trafficking, and migration. A net forest cover loss in the municipality of Calakmul is particularly concerning because it hosts the entire core and majority of the buffer zone of CBR and has received a significant share of national REDD+ investments. The municipality of Champotón was the second with the most REDD+ initiatives, and together with Escárcega, it has an essential role in the state's forestry sector, and both experienced the positive effect of REDD+. Although REDD+ interventions did not reduce forest cover loss in the municipality of Hopelchén, some communities implementing silvopastoral and conservation agriculture projects did experience a positive trend in deforestation rate.


We used a literature review with key criteria from a systematic review (Haddaway et al., 2015, 2020) to analyze which forest cover change processes caused by productive activities were identified, described, and evaluated in the Calakmul Biosphere Reserve, including its broader transition area. Most investigations in our study area focused on deforestation, which was evident by the highest frequency of codes assigned to this process in the entire sample. Also, the majority of primary studies focused on deforestation. Although they are sometimes recognized as present in the dynamic CBR forest landscape, other forest cover change processes were less evidenced in the literature. The majority of the studies use a quantitative methodology to evaluate the changes in the forest cover. They do so at a scale of the Southern Yucatán region, which includes the municipality of Calakmul and the southeast portion of Quintana Roo (Turner, 2010), and consider productive activities only as one of the land uses. Nevertheless, the heterogeneity in spatial and temporal scales between studies did not allow for a meta-analysis.

The tendency to document deforestation is common in the global tropics (Borda-Niño et al., 2020). This trend can be explained by the alarming global forest loss (Gibbs et al., 2010; Keenan et al., 2015). However, the focus on deforestation can mask the presence or importance of other forest cover change processes, such as forest degradation in particular. According to a study performed in the neighboring state of Quintana Roo by Ellis, Navarro Martínez, et al. (2020), forest degradation might be the most dominant process in our study area too. The authors acknowledge that besides more precise remote sensing methods, the understating of agricultural activities at the local level allowed them to differentiate the long-term (deforestation) from temporary forest losses (degradation).

In other words, in shifting cultivation, deforestation and forest succession are part of a single cycle that is considered sustainable if the optimal balance between cropping and fallow time is maintained (Altieri & Toledo, 2005). However, the shortening of fallow resulting from population increase and agricultural intensification in the study area (Dobler-Morales et al., 2020; Porter-Bolland et al., 2008) pushed forests toward degradation. This occurs when the ecosystem does not have time to recover minimal levels of biomass, biodiversity, and nutrients necessary for its normal functioning (Ghazoul et al., 2015). Similarly, pasture establishment truncates the succession cycle in the area that could potentially grow in secondary forests, moving this way from forest degradation to deforestation.

Although productive activities might cause both negative and positive forest cover change processes, the investigations in our study area focused more on the former. They analyzed commercial agriculture and big livestock breeding as the cause of deforestation and selective logging and subsistence agriculture as the cause of forest degradation. In addition, the studies showed that pasture abandonment did not result in forest recovery but in another negative forest process instead: arrested succession, that is, an invasive species-dominated ecosystem remaining a long time in an early succession state (Thrippleton et al., 2018).

However, many other identified activities and practices concerning forest degradation were not empirically documented. In particular, the misuse of fire in livestock activity that can be considered a driver of degradation was not documented. More severe forest fires might also provoke more permanent land-use changes. Similarly, high-impact logging practices aggravate degradation more immediately, but the associated road infrastructure might encourage deforestation for commercial agriculture expansion. However, forest degradation not always has negative repercussions. For instance, shorter fallows result in an abundance of invasive species of sunflower goldeneye that is an essential source of nectar for honey production in the region (Cázares et al., 2016), which in turn incentivizes forest conservation.

Although much less evidenced in the studies, forest conservation and recovery occur parallel to the negative forest cover change processes. The large forest areas in the CBR region bear witness to this. The forest preservation has to do with Calakmul's status as BR, which includes zones obeying more or less restrictive rules. Biosphere reserves in Mexico have particularly complex zoning because they are usually established on historically occupied land under social ownership, which restricts local owners' use of forest resources (Durand & Jímenez, 2010). The establishment of CBR in 1989 implied a series of agreements, rearrangements, and conflicts in land-use planning and the regulation of productive activities (Levy-Tacher et al., 2019; Oliva et al., 2020). The CBR zoning resulted in the ‘humanless' core zone experiencing the recovery of mature forests (Porter-Bolland et al., 2015). In contrast, the intensification of productive activities resulted in negative forest cover change processes in buffer and transition zones (Schmook & Vance, 2009). In addition, the government promoted the eco-archaeo-tourisms projects as compatible with conservation policies and agricultural incentives (Manson, 2006). However, the tourist influx increases the probability of forest fires and contamination from waste accumulation in open garbage dumps (Rada et al., 2015). In addition, the economic gains from tourism might not be sufficient to outweigh monetary and cultural losses due to restrictions on traditional productive activities (Quadri-Barba et al., 2021; Turner et al., 2003).

Agricultural intensification was considered a viable solution for achieving both conservation and productive objectives of CBR. Consequently, subsidies and regulations incentivized these activities (Dobler-Morales et al., 2020). Therefore, it is not surprising that more than 90% of the revised publications focus on the period after the 1970s when the green revolution had already been going on in Mexico for three decades (González, 2006). The main drivers of deforestation in the municipality of Calakmul were subsistence and the commercial production performed by ejidos. In Hopelchén, in contrast, the most deforestation was reported in private property land owned by Mennonite industrialized farmers. In both cases, the intensified commercial agriculture did not manage to spare forest cover. Instead, the prospect of more profit prompted the ejidos to expand mechanized agriculture to flat areas of forest extension allotted to them in the past to support traditional shifting agriculture and timber harvesting activities that were once the most dominant (Cantún & Pat, 2012).

Despite the expansion of cattle-raising, this activity is performed largely for commercialization, and the local population continues to be dependent on meat hunting for subsistence (Roy Chowdhury et al., 2006). Hunting can negatively impact the forest when it includes the use of fire (Rada et al., 2015). On the other hand, agricultural development could also affect hunting, for less (dense) forest means less habitat for the wildlife species (Escamilla et al., 2000).

Despite its great importance in assuring the achievement of the BR objectives, our sample investigated the transition zone to a smaller extent. This zone is also called the area of influence, which explains well the bidirectionality of impact between BR (core and buffer) and surrounding (transition) areas under public policies and non-policy factors identified in the literature. However, except for the municipality of Calakmul, there is a lack of initiatives to develop local institutions that could promote productive activities compatible with conservation in the other four municipalities that host the CBR transition area (see Porter-Bolland et al., 2008).

In addition, and according to Klepeis (2003), during a large part of the 20th century, local people played only a passive role in land management decisions in the study region. Although the current design of the REDD+ recognizes local forest owners as direct implementers and beneficiaries of forestry programs, the federal government designed and implemented them with national and international money. Furthermore, REDD+ has predominantly focused on reducing deforestation through payments to traditional farmers for ecosystem services (Kelly, 2020). However, industrial farmers are the main forest loss drivers (Skutsch & Turnhout, 2020).

With or without REDD+, the traditional small farmers contribute to forest conservation and succession processes through their traditional productive systems. Traditional agroforestry and beekeeping are well-known for their adaptability to changing socio-economic conditions (Bareke et al., 2021; Jose, 2019). The heterogeneity of forest covers and the diversity of practices are observed at the ejido scale (Rueda, 2010). However, in our study area, positive forest cover change processes were investigated as coupled with negative processes at state and regional scales. Therefore, those positive processes occurring at the local scale stay unperceived. Future investigations should focus on sustainable activities related to positive forest cover change processes at the local level to fill this research gap.

Implications for Conservation

Since the 1960s, the Mexican government has targeted the broader Calakmul area for rural development (timber harvesting, agriculture, livestock breeding) and conservation activities (Biosphere Reserve). However, the design of development programs did not include an environmental perspective. Although many ejidos have valid governmental permits, timber harvesting is considered unprofitable. This productive activity is currently performed only by a few ejidos, the same who can afford RIL practices to reduce forest degradation. Governmental policies should consider monetary resources and technical assistance supporting RIL practices, and CFM in forest ejidos should be promoted to increase local timber competitiveness in the national and international market.

Even though the latest agricultural programs focus on intensification to yield more from less land, they continue contributing to deforestation because they do not include in their design low-impact organic inputs (e.g., green compost) and technology (e.g., small tractors), nor do they account for other important local socio-economic factors, such as land and labor availability. The shortening of fallows can be addressed by either targeting its biological efficiency (weed control and soil fertility improvements) or by increasing its economic value (commercial species), also known as improved fallows (manejo de acahuales in Spanish), a local agroforestry practice (Soto Pinto et al., 2011).

REDD+ promoted silvopastoral systems and conservation agriculture, which significantly reduced deforestation when combined with productive forestry (Ellis, Sierra-Huelsz, et al., 2020). To make these activities more attractive to farmers, their design should be based on the traditional agrosilvopastoral systems, and they should grant enough payments to cover transaction costs and leave net benefits. In addition, beekeeping as an economically viable activity should be supported by providing equipment and helping revive beekeepers' associations.

However, the Mennonites' pressure that makes unsustainable agriculture more profitable to ejidos may diminish these efforts. The unsustainable behaviors of industrial farmers should, thus, be controlled with stricter implementation of environmental and agrarian laws and by their inclusion in participatory spaces where sustainable rural development of the broader Calakmul area is discussed.

Finally, more empirical studies are needed to make forest conservation and development efforts visible. For example, longitudinal mixed-methods studies should be performed (e.g., Dobler-Morales, 2019 in; Dobler-Morales, 2021) to evaluate non-conventional agricultural activities and forest regeneration and reforestation efforts, including the newest governmental agroforestry development program Sembrando Vida (Planting Life) that was launched in 2018. These studies will allow learning from the experience and promote public policy instruments' design for resilient and inclusive growth in the Calakmul Biosphere Reserve's broader area.

Declaration of Conflicting Interests The author(s) declared no potential conflicts of interest with respect to the research, authorship, and/or publication of this article.

Funding The author(s) disclosed receipt of the following financial support for the research, authorship, and/or publication of this article: The PAPIIT-UNAM project IT300221 financially supported this work. Jovanka Špirić acknowledges the support of the CONACYT Cátedra project 1539 in carrying out this work. The authors are grateful to the editor and four anonymous reviewers for their constructive comments and suggestions.

Supplemental Material Supplemental material for this article is available online.



Abizaid C., Coomes O. T. (2004). Land use and forest fallowing dynamics in seasonally dry tropical forests of the southern Yucatán Peninsula, Mexico. Land Use Policy, 21(1), 71–84. Google Scholar


Alonso Velasco I. (2020). Migraciones y colonización de un territorio bajo disputa territorial en la Península de Yucatán, México. TERRA: Revista de Desarrollo Local, 7(7), 96–118. Google Scholar


Altieri M. A., Toledo V. M. (2005). Natural resource management among small-scale farmers in semi-arid lands: Building on traditional knowledge and agroecology. Annals of Arid Zone, 44(3&4), 365–385. Google Scholar


Angelsen A. (2008). In Angelsen A. (Ed.), Moving ahead with REDD: Issues, options and implications. Center for International Forestry Research. Google Scholar


Armenta-Montero S., Ellis E. A., Ellis P. W., Manson R. H., López-Binnqüist C., Pérez J. A. V. (2020). Carbon emissions from selective logging in the southern yucatan Peninsula, Mexico. Madera Y Bosques, 26(1), 1. Google Scholar


Arroyo-Rodríguez V., Dias P. A. D. (2010). Effects of habitat fragmentation and disturbance on howler monkeys: A review. American Journal of Primatology, 72(1), 1–16. Google Scholar


Aryal D. R., de Jong B. H. J., Ochoa-Gaona S., Esparza-Olguin L., Mendoza-Vega J. (2014). Carbon stocks and changes in tropical secondary forests of southern Mexico. Agriculture, Ecosystems and Environment, 195(1), 220–230. Google Scholar


Baccini A., Walker W., Carvalho L., Farina M., Sulla-Menashe D., Houghton R. A. (2017). Tropical forests are a net carbon source based on aboveground measurements of gain and loss. Science, 358(6360), 230–234. Google Scholar


Bareke T., Gemeda M., Kumsa T., Addi A., Endale W. (2021). Beekeeping as an incentive to catchment rehabilitation. International Journal of Environmental Studies, 1, 1–11. Google Scholar


Bayrak M. M., Marafa L. M. (2016). Ten years of REDD+: A critical review of the impact of REDD+ on forest-dependent communities. Sustainability, 8(7), 1–22. Google Scholar


Bezaury-Creel J., Gutiérrez Carbonell D. (2009). Áreas naturales protegidas y desarrollo social en México. Estado de conservación y tendencias de cambio, 3(1), 387–420. Google Scholar


Borda-Niño M., Meli P., Brancalion P. H. S. (2020). Drivers of tropical forest cover increase: A systematic review. Land Degradation & Development, 31(11), 1366–1379. Google Scholar


Bridgewater P. (2016). The man and biosphere program of UNESCO: Rambunctious child of the sixties, but was the promise fulfilled? Current Opinion in Environmental Sustainability, 19(1), 1–6. Google Scholar


Busch C., Geoghegan J. (2010). Labor scarcity as an underlying cause of the increasing prevalence of deforestation due to cattle pasture development in the southern Yucatán region. Regional Environmental Change, 10(3), 191–203. Google Scholar


Busch C. B., Vance C. (2011). The diffusion of cattle ranching and deforestation: Prospects for a hollow frontier in Mexico’s yucatán. Land Economics, 87(4), 682–698. Google Scholar


Cantún M. C., Pat J. M. F. (2012). The agrarian reform in Campeche, continuation of an indigenous culture? Secuencia, 82(1), 101–126. Google Scholar


Casey J. F., Caviglia J. L. (2000). Deforestation and agroforestry adoption in tropical forests: Can we generalize? Some results from Campeche, Mexico and rondônia, Brazil. In WesternAgricultural economics association annual meetings (Vol. 1–26). Google Scholar


Cázares C. A. V., Ordóñez M. Y. B., Cruz C. M. A., Huerta E. E., Velasco A. M. E., Avilés M. M. A. (2016). Composición botánica de mieles de la península de Yucatán, mediante qPCR y análisis de curvas de disociación. Revista Mexicana de Ciencias Pecuarias, 7(4), 489–505. Google Scholar


Chará J., Reyes E., Peri P., Otte J., Arce E., Schneider F. (2020). Sistemas silvopastoriles y su contribución al uso eficiente de los recursos y a los Objetivos de Desarrollo Sostenible: Evidencia desde América Latina. FAO, Editorial CIPAV & Agri Benchmark. Google Scholar


Cheng D., Rogan J., Schneider L., Cochrane M. (2013). Evaluating MODIS active fire products in subtropical yucatán forest. Remote Sensing Letters, 4(5), 455–464. Google Scholar


Choocharoen C., Neef A., Preechapanya P., Hoffmann V. (2014). Agrosilvopastoral systems in northern Thailand and northern Laos: Minority peoples’ knowledge versus government policy. Land, 3(2), 414–436. Google Scholar


Chowdhury R. R. (2007). Household land management and biodiversity: Secondary succession in a forest-agriculture mosaic in southern Mexico. [Eye Science Electronic Resource], 12(2), 1. Google Scholar


CONAFOR (2015). Intervention model in Redd+ early action areas. Google Scholar


CONAFOR (2017a). Documento de la Iniciativa de Reducción de Emisiones (IRE) ER program name and country: México. Google Scholar


CONAFOR (2017b). Estrategia Nacional para REDD+ México 2017-2030 ENAREDD+. Google Scholar


CONAFOR (2020). Nivel de Referencia de Emisiones forestales de México (2007-2016. Google Scholar


CONANP (2022). Áreas naturales protegidas decretadas. Google Scholar


CONEVAL (2020). Medición de pobreza municipal. Google Scholar


de Jong B. H. (2013). Spatial distribution of biomass and links to reported disturbances in tropical lowland forests of southern Mexico. Carbon Management, 4(6), 601–615. Google Scholar


Díaz Gallegos J. R., García Gil G., Castillo Acosta O., March Mifsut I. (2001). Uso del suelo y transformación de selvas en un ejido de la Reserva de la Biosfera Calakmul, Campeche, México Investigaciones geográficas (44, pp. 39–53). Boletín Del Instituto de Geografía, UNAM. Google Scholar


Díaz-Gallegos J. R., Mas J.-F., Velázquez Montes A. (2008). Monitoreo de los patrones de deforestación en el Corredor Biológico Mesoamericano. Interciencia, 33, 882–890. Google Scholar


Dobler-Morales C. (2019). Smallholder dimensions of rural change in modern Mexico (PhD Dissertation). Clark University. Google Scholar


Dobler-Morales C. (2021). Between subsidies and parks: The impact of agrarian and conservation policy on smallholder territories of Calakmul, Mexico. In McCall M. K., Boni Noguez A., Napoletano B., Rico-Rodríguez T. (Eds.), Territorialising space in Latin America (pp. 57–73). Springer Nature Switzerland. Google Scholar


Dobler-Morales C., Roy Chowdhury R., Schmook B. (2020). Governing intensification: The influence of state institutions on smallholder farming strategies in Calakmul, Mexico. Journal of Land Use Science, 15(2–3), 108–126. Google Scholar


Durand L., Jímenez J. (2010). Sobre áreas naturales protegidas y la construcción de no-lugares. Notas para México. Revista Lider, 16, 59–72. Google Scholar


Eaton J. M., Lawrence D. (2009). Loss of carbon sequestration potential after several decades of shifting cultivation in the Southern Yucatán. Forest Ecology and Management, 258(6), 949–958. Google Scholar


Ellis E. A., Hernandez Gomez U., Romero-Montero J. A. (2017a). Los procesos y causas del cambio en la cobertura forestal de la Península Yucatán, México. Ecosistemas, 26(1), 101–111. Google Scholar


Ellis E. A., Montero S. A., Hernández Gómez I. U., Romero Montero J. A., Ellis P. W., Rodríguez-Ward D., Blanco Reyes P., Putz F. E. (2019). Reduced-impact logging practices reduce forest disturbance and carbon emissions in community managed forests on the Yucatán Peninsula, Mexico. Forest Ecology and Management, 437(1), 396–410. Google Scholar


Ellis E. A., Navarro Martínez A., García Ortega M., Hernández Gómez I. U., Chacón Castillo D. (2020b). Forest cover dynamics in the selva maya of central and southern Quintana Roo, Mexico: Deforestation or degradation? Journal of Land Use Science, 15(1), 25–51. Google Scholar


Ellis E. A., Porter-Bolland L. (2008). Is community-based forest management more effective than protected areas? A comparison of land use/land cover change in two neighboring study areas of the Central Yucatan Peninsula, Mexico. Forest Ecology and Management, 256(11), 1971–1983. Google Scholar


Ellis E. A., Romero-Montero J. A., Hernández-Gómez I. U. (2015). Evaluación y mapeo de los determinantes de la deforestación en la Península Yucatán. Agencia de los Estados Unidos para el Desarrollo Internacional (USAID), the Nature Conservancy (TNC), Alianza México REDD+, México, Distrito Federal. Google Scholar


Ellis E. A., Romero Montero J. A., Hernández Gómez I. U., Porter-Bolland L., Ellis P. W. (2017b). Private property and Mennonites are major drivers of forest cover loss in central Yucatan Peninsula, Mexico. Land Use Policy, 69(1), 474–484. Google Scholar


Ellis E. A., Sierra-Huelsz J. A., Ceballos G. C. O., Binnqüist C. L., Cerdán C. R. (2020a). Mixed effectiveness of REDD+ subnational initiatives after 10 years of interventions on the Yucatan Peninsula, Mexico. Forests, 11(9), 1005. Google Scholar


Escamilla A., Sanvicente M., Sosa M., Galindo-Leal C. (2000). Habitat mosaic, wildlife availability, and hunting in the tropical forest of Calakmul, Mexico. Conservation Biology, 14(6), 1592–1601. Google Scholar


FAO (2007). Manual on deforestation, degradation, and fragmentation using remote sensing and GIS. Google Scholar


FAO (2020b). Global forest resource assessment 2020. Terms and definitions. Food and Agriculture Organization, Working Paper 188 Google Scholar


FAO (2020a). Global forest resources assessment 2020. FAO. Google Scholar


Fitzherbert E. B., Struebig M. J., Morel A., Danielsen F., Brühl C. A., Donald P. F., Phalan B. (2008). How will oil palm expansion affect biodiversity? Trends in Ecology & Evolution, 23(10), 538–545. Google Scholar


García-Barrios L., Galván-Miyoshi Y. M., Valsieso-Pérez I. A., Masera O. R., Bocco G., Vandermeer J. (2009). Neotropical forest conservation, agricultural intensification, and rural out-migration: The Mexican experience. BioScience, 59(10), 863–873. Google Scholar


García Gil G., March I. M., Castillo M. Á. S. (2001). Transformación de la vegetación por cambio de uso del suelo en la Reserva de la Biosfera Calakmul, Campeche Vegetation change resulting from the change in soil use in the Calakmul Biosphere Reserve, Campeche In Investigaciones geográficas (46, pp. 45–57). Boletín Del Instituto de Geografía, UNAM. Google Scholar


Geoghegan J., Lawrence D., Schneider L. C., Tully K. (2010). Accounting for carbon stocks in models of land-use change: An application to Southern Yucatan. Regional Environmental Change, 10(3), 247–260. Google Scholar


GFW (2020). México. Google Scholar


Ghazoul J, Burivalova Z, Garcia-Ulloa J, King LA (2015). Conceptualizing forest degradation. Trends in Ecology & Evolution, 30(10), 622–632. Google Scholar


Gibbs HK, Ruesch AS, Achard F, Clayton MK, Holmgren P, Ramankutty N, Foley JA (2010). Tropical forests were the primary sources of new agricultural land in the 1980s and 1990s. Proceedings of the National Academy of Sciences, 107(38), 16732–16737. Google Scholar


González B. P. (2006). La revolución verde en México. Agrária (São Paulo. Online), 4(1), 40–68. Google Scholar


Grant MJ, Booth A (2009). A typology of reviews: And analysis of 14 review types and associated methodologies. Health Information and Libraries Journal, 26(2), 91–108. Google Scholar


Griscom B., Ganz D., Virgilio N., Price F., Hayward J., Cortez R., Dodge G., Hurd J., Lowenstein F. L., Stanley B. (2009). The hidden frontier of forest degradation: A review of the science, policy and practice of reducing degradation emissions. The Nature Conservancy, Epub ahead of print. Google Scholar


Haddaway N. R., Bethel A., Dicks L. V., Koricheva J., Macura B., Petrokofsky G., Pullin A. S., Savilaakso S., Stewart G. B. (2020). Eight problems with literature reviews and how to fix them. Nature Ecology and Evolution, 4(12), 1582–1589. Google Scholar


Haddaway N. R., Woodcock P., Macura B., Collins A. (2015). Making literature reviews more reliable through application of lessons from systematic reviews. Conservation Biology, 29(6), 1596–1605. Google Scholar


Halffter G. (1984). Las Reservas de la Biosfera: Conservación de la Naturaleza para el Hombre. Acta Zoológica Mexicana, 5(1), 1–50. Google Scholar


Honey-Rosés J., Maurer M., Ramírez M. I., Corbera E. (2018). Quantifying active and passive restoration in central Mexico from 1986-2012: Assessing the evidence of a forest transition. Restoration Ecology, 26(6), 1180–1189. Google Scholar


Hosonuma N., Herold M., De Sy V., de Fries R. S., Brockhaus M., Verchot L., Angelsen A., Romijn E. (2012). An assessment of deforestation and forest degradation drivers in developing countries. Environmental Research Letters, 7(4), 044009. Google Scholar


Humphreys D. (2006). Logjam. Deforestation and the crisis of global governance. Earthscan. Google Scholar


INAFED (2022). Enciclopedia de los Municipios y Delegaciones de México. Campeche. Google Scholar


INEGI (2020). Censo de Población y vivienda 2020. Google Scholar


IPCC (2021). Climate change 2021: The physical science basis. Summary for policymakers. Contribution of working group I to the sixth assessment report of the intergovernmental panel on climate change. Google Scholar


Jose S. (2019). Environmental impacts and benefits of agroforestry. In Oxford research encyclopedia of environmental science. Oxford University Press. Google Scholar


Keenan R. J., Reams G. A., Achard F., de Freitas J. v., Grainger A., Lindquist E. (2015). Dynamics of global forest area: Results from the FAO global forest resources assessment 2015. Forest Ecology and Management, 352(7), 9–20. Google Scholar


Kelly J. (2020). Village-scale reserves in the forest frontier regions of Chenes and Calakmul, Mexico. Journal of Land Use Science, 15(2–3), 203–220. Google Scholar


Keys E. (2005). Exploring market-based development: Market intermediaries and farmers in Calakmul, Mexico. Geographical Review, 95(1), 24–46. Google Scholar


Keys E. (2010). Hurdles to forest friendly farming: Sustainability lessons from southeastern Mexico. Sustainability, 2(9), 3129–3141. Google Scholar


Klepeis P. (2003). Development policies and tropical deforestation in the southern Yucatán Peninsula: Centralized and decentralized approaches. Land Degradation and Development, 14(6), 541–561. Google Scholar


Krylov A., Steininger M. K., Hansen M. C., Potapov P. v., Stehman S. v., Gost A., Noel J., Talero Ramirez Y., Tyukavina A., di Bella C. M., Ellis E. A., Ellis P. (2018). Contrasting tree-cover loss and subsequent land cover in two neotropical forest regions: Sample-based assessment of the Mexican yucatán and Argentine chaco. Journal of Land Use Science, 13(6), 549–564. Google Scholar


Lambin E. F., Meyfroidt P. (2011). Global land use change, economic globalization, and the looming land scarcity. Proceedings of the National Academy of Sciences, 108(9), 3465–3472. Google Scholar


Lambin E. F., Geist H. J., Lepers E. (2003). Dynamics of land-use and land-cover change in tropical regions. Annual Review of Environment and Resources, 28(1), 205–241. Google Scholar


Laurance W. F. (2015). Emerging threats to tropical forests. Annals of the Missouri Botanical Garden, 100(3), 159–169. Google Scholar


Levy-Tacher S. I., Ramírez-Marcial N., Navarrete-Gutiérrez D. A., Rodríguez-Sánchez P. V. (2019). Are Mayan community forest reserves effective in fulfilling people’s needs and preserving tree species? Journal of Environmental Management, 245(1), 16–27. Google Scholar


Ley Agraria (2018). Nueva ley publicada en el diario oficial de la federación el 26 de febrero de 1992, TEXTO VIGENTE, Última reforma publicada. DOF 25-06-2018 Google Scholar


Madrid R. L. (2020). REDD+: Base construida, retos y lecciones aprendidas en México. Google Scholar


Manson S. (2006). Land use in the southern Yucatán peninsular region of Mexico: Scenarios of population and institutional change. Computers, Environment and Urban Systems, 30(3), 230–253. Google Scholar


Mascorro V. S., Coops N. C., Kurz W. A., Olguín M. (2016). Attributing changes in land cover using independent disturbance datasets: A case study of the yucatan Peninsula, Mexico. Regional Environmental Change, 16(1), 213–228. Google Scholar


Mather A. S., Needle C. L. (1998). The forest transition: A theoretical basis. Area, 30(2), 117–124. Google Scholar


Morales-Barquero L., Borrego A., Skutsch M., Kleinn C., Healey J. R. (2014). Identification and quantification of drivers of forest degradation in tropical dry forests: A case study in western Mexico. Land Use Policy, 49(1), 296–309. Google Scholar


Moreno-Calles A. I., Casas A., Rivero-Romero A. D., Romero-Bautista Y. A., Rangel-Landa S., Fisher-Ortíz R. A., Alvarado-Ramos F., Vallejo-Ramos M., Santos-Fita D. (2016). Ethnoagroforestry: Integration of biocultural diversity for food sovereignty in Mexico. Journal of Ethnobiology and Ethnomedicine, 12(1), 54. Google Scholar


Navarrete J.-L., Isabel Ramírez M., Pérez-Salicrup D. R. (2011). Logging within protected areas: Spatial evaluation of the monarch butterfly biosphere reserve, Mexico. Forest Ecology and Management, 262(4), 646–654. Google Scholar


Neeti N., Rogan J., Christman Z., Eastman J. R., Millones M., Schneider L., Nickl E., Schmook B., Turner B. L., Ghimire B. (2012). Mapping seasonal trends in vegetation using AVHRR-NDVI time series in the Yucatán Peninsula, Mexico. Remote Sensing Letters, 3(5), 433–442. Google Scholar


Oliva M., García-Frapolli E., Porter-Bolland L., Montiel S. (2020). Dis)agreements in the management of conservation conflicts in the Calakmul Biosphere Reserve, Mexico. Environmental Conservation, 47(4), 295–303. Google Scholar


Osborne T., Bellante L., vonHedemann N. (2014). Indigenous peoples and REDD+: A critical perspective indigenous Peopleʼs biocultural climate change assessment initiative. IPCCA and The Christensen Fund. Google Scholar


Otero G. (2014). La dieta neoliberal: Globalización y biotecnología agrícola en las américas. Miguel Ángel Porrúa. Google Scholar


Pearson T. R. H., Brown S., Murray L., Sidman G. (2017). Greenhouse gas emissions from tropical forest degradation: An underestimated source. Carbon Balance and Management, 12(1), 3. Google Scholar


Pérez P. J., Merino M. (2016). Definición de Sector primario. Definicion.De. Google Scholar


Porter Bolland L. (2003). La apicultura y el paisaje maya. Estudio sobre la fenología de floración de las especies melíferas y su relación con el ciclo apícola en La Montaña, Campeche, México. Mexican Studies/Estudios Mexicanos, 19(2), 303–330. Google Scholar


Porter-Bolland L., Bonilla-Moheno M., Garcia-Frapolli E., Morteo-Montiel S. (2015). Forest ecosystems and conservation In Biodiversity and conservation of the yucatan Peninsula (pp. 377–398). Springer International Publishing. Google Scholar


Porter-Bolland L., Ellis E. A., Gholz H. L. (2007). Land use dynamics and landscape history in La Montaña, Campeche, Mexico. Landscape and Urban Planning, 82(4), 198–207. Google Scholar


Porter-Bolland L., Sánchez González M. C., Ellis E. A. (2008). La conformación del paisaje y el aprovechamiento de los recursos naturales por las comunidades mayas de La Montaña, Hopelchén, Campeche. Investigaciones Geográficas (66, pp. 65–80). Boletín Del Instituto de Geografía, UNAM. Google Scholar


Quadri-Barba P., Sims K. R. E., Millard-Ball A. (2021). Using cultural heritage sites in Mexico to understand the poverty alleviation impacts of protected areas. Conservation Science and Practice, 3(2), Article e339. Google Scholar


Rada J. M. D., García R. D., García-Contreras G., Morín J. A., Lugo E. A., González M. E. M., Hernández M. A. (2015). Conservation and use. In: Biodiversity and conservation of the Yucatán Peninsula (pp. 169–193). Springer. Google Scholar


Radel C., Schmook B. (2008). Male transnational migration and its linkages to land-use change in a southern Campeche ejido. Journal of Latin American Geography, 7(2), 59–84. Google Scholar


Radel C., Schmook B., Chowdhury R. R. (2010a). Agricultural livelihood transition in the southern Yucatán region: Diverging paths and their accompanying land changes. Regional Environmental Change, 10(3), 205–218. Google Scholar


Radel C., Schmook B., McCandless S. (2010b). Environment, transnational labor migration, and gender: Case studies from southern yucatán, Mexico and Vermont, USA. Population and Environment, 32(2), 177–197. Google Scholar


Ramankutty N., Graumlich L., Achard F., Alves D., Chhabra A., DeFries R. S., Foley J.A., Geist H., Houghton R. A., Goldewijk K. K., Lambin E. F., Millington A., Rasmussen K., Reid R. S., Turner B. L.II (2010). Global land-cover change: Recent progress, remaining challenges. In Lambin E. F., Geist H. J. (Eds.), Land-use and land-cover change. Local processes and global impacts (pp. 9–39). Springer. Google Scholar


Ramírez M. I., Sáenz-Romero C., Rehfeldt G., Salas-Canela L. (2015). Threats to the availability of overwintering habitat in the monarch butterfly biosphere reserve land use and climate change. In Oberhauser K. S., Nail K. R., Altizer S. (Eds.), Monarchs in a changing world. Biology and conservation of an iconic butterfly (pp. 157–312). Cornell University Press. Google Scholar


Ramírez-Delgado J. P., Christman Z., Schmook B. (2014). Deforestation and fragmentation of seasonal tropical forests in the southern Yucatán, Mexico (1990-2006). Geocarto International, 29(8), 822–841. Google Scholar


Read L., Lawrence D. (2003). Recovery of biomass following shifting cultivation in dry tropical forests on the yucatan. Ecological Applications, 13(1), 85–97.[0085:ROBFSC]2.0.CO;2 Google Scholar


Reyes-Hernández H., Cortina-Villar S., Perales-Rivera H., Kauffer-Michel E., Pat-Fernández J. M. (2003). Efecto de los subsidios agropecuarios y apoyos gubernamentales sobre la deforestación durante el período 1990-2000. In Investigaciones geográficas (51, pp. 88–106). Boletín Del Instituto de Geografía, UNAM. Google Scholar


Rodríguez-Solorzano C. (2014). Unintended outcomes of farmers’ adaptation to climate variability: Deforestation and conservation in Calakmul and Maya biosphere reserves. [Eye Science Electronic Resource], 19(2), 1. Google Scholar


Rodríguez-Trejo D. A., Tchikoué H., Cíntora-González C., Contreras-Aguado R., de la Rosa-Vázquez A. (2011). Modelaje del peligro de incendio forestal en las zonas afectadas por el huracán Dean. Agrociencias, 45(1), 593–608. Google Scholar


Román-Dañobeytia F. J., Levy-Tacher S. I., Macario-Mendoza P., Zúñiga-Morales J. (2014). Redefining secondary forests in the Mexican forest code: Implications for management, restoration, and conservation. Forests, 5(5), 978–991. Google Scholar


Roy Chowdhury R. (2006). Landscape change in the Calakmul Biosphere Reserve, Mexico: Modeling the driving forces of smallholder deforestation in land parcels. Applied Geography, 26(2), 129–152. Google Scholar


Roy Chowdhury R (2010). Differentiation and concordance in smallholder land use strategies in southern Mexico’s conservation frontier. Proceedings of the National Academy of Sciences of the United States of America, 107(13), 5780–5785. Google Scholar


Roy Chowdhury R., Turner B. L.II (2006). Reconciling agency and structure in empirical analysis: Smallholder land use in the southern yucatán, Mexico. Annals of the Association of American Geographers, 96(2), 302–322. Google Scholar


Rudel T. K., Coomes O. T., Moran E., Achard F., Angelsen A., Xu J., Lambin E. (2005). Forest transitions: Towards a global understanding of land use change. Global Environmental Change, 15(1), 23–31. Google Scholar


Rueda X. (2010). Understanding deforestation in the southern Yucatán: Insights from a sub-regional, multi-temporal analysis. Regional Environmental Change, 10(3), 175–189. Google Scholar


Salaheen S., Biswas D. (2019). Organic farming practices: Integrated culture versus monoculture. Safety and Practice for organic food (pp. 23–32). Google Scholar


Saldana J. (2015). The coding manual for qualitative researchers (3rd ed.). Sage. Google Scholar


Schmook B., Palmer Dickson R., Sangermano F., Vadjunec J. M., Eastman J. R., Rogan J. (2011). A step-wise land-cover classification of the tropical forests of the Southern Yucatán, Mexico. International Journal of Remote Sensing, 32(4), 1139–1164. Google Scholar


Schmook B., Radel C. (2008). International labor migration from a tropical development frontier: Globalizing households and an incipient forest transition: The Southern Yucatán case. Human Ecology, 36(6), 891–908. Google Scholar


Schmook B., Vance C. (2009). Agricultural policy, market barriers, and deforestation: The case of Mexico’s southern yucatán. World Development, 37(5), 1015–1025. Google Scholar


Schramski S., Keys E. (2013). Smallholder response to hurricane dean: Creating new human ecologies through charcoal production. Natural Hazards Review, 14(4), 211–219. Google Scholar


Skutsch M., Turnhout E. (2020). REDD+: If communities are the solution, what is the problem? World Development, 130(1), 104942. Google Scholar


Skutsch M. M., McCall M. K., Karky B., Zahabu E., Peters-Guarin G. (2009). Case studies on measuring and assessing forest degradation. Community Measurement of Carbon Stock Chang for REDD. + (No. 156) Google Scholar


Soto Pinto L., Anzueto Martínez M., Quechulpa S. (2011). El acahual mejorado. Un prototipo agroforestal. ECOSUR & redISA. Google Scholar


Thornton P. K. (2010). Livestock production: Recent trends, future prospects. Philosophical Transactions of the Royal Society B: Biological Sciences, 365(1554), 2853–2867. Google Scholar


Thrippleton T., Bugmann H., Snell R. S. (2018). Herbaceous competition and browsing may induce arrested succession in central European forests. Journal of Ecology, 106(3), 1120–1132. Google Scholar


Trondoli M. E. A., Lewis S. D., Bueno C. O., Antonio P. M., Howard S. J., Pereira M. E. (2020). Long-term forest degradation surpasses deforestation in the Brazilian Amazon. Science, 369(6509), 1378–1382. Google Scholar


Turner B.II Geoghegan J., Lawrence D., Radel C., Schmook B., Vance C., Manson S., Keys E., Foster D., Klepeis P., Vester H., Rogan J., Roy Chowdhury R., Schneider L., Dickson R., Ogenva-Himmelberger Y. (2016). Land system science and the social-environmental system: The case of Southern Yucatán Peninsular Region (SYPR) project. Current Opinion in Environmental Sustainability, 19(1), 18–29. Google Scholar


Turner B. L.II (2010). Land change in the southern Yucatán: Case studies in land change science. Regional Environmental Change, 10(3), 169–174. Google Scholar


Turner B. L.II Cortina Villar S., Foster D., Geoghegan J., Keys E., Klepeis P., Lawrence D., Mendoza P. M., Manson S., Ogneva-Himmelberger Y., Plotkin A. B., Pérez Salicrup D., Chowdhury R. R., Savitsky B., Schneider L., Schmook B., Vance C. (2001). Deforestation in the southern Yucatán peninsular region. An integrative approach. Forest Ecology and Management, 5521(1), 1–18. Google Scholar


Turner BLII Matson PA, McCarthy JJ, Corell RW, Christensen L, Eckley N, Hovelsrud-Broda GK, Kasperson JX, Kasperson RE, Luers A, Martello ML, Mathiesen S, Naylor R, Polsky C, Pulsipher A, Schiller A, Selin H, Tyler N (2003). Illustrating the coupled human-environment system for vulnerability analysis: Three case studies. Proceedings of the National Academy of Sciences of the United States of America, 100(14), 8080–8085. Google Scholar


UNESCO (1996). Reservas de biosfera: La Estrategia de Sevilla y el Marco Estatutario de la Red Mundial. Google Scholar


UNESCO (2014). Decisions adopted by the world heritage committee at its 38th session (doha, 2014). Google Scholar


UNESCO (2017). A new roadmap for the man and the biosphere (MAB) programme and its world network of biosphere reserves. Google Scholar


UNESCO (2021). Technical guidelines for biosphere reserves. Google Scholar


UNFCCC (2002). Glasgow leaders’ declaration on forests and land use. UN climate change conference UK 2021. COP 26. Google Scholar


UNFCCC (2010). Report of the conference of the parties serving as the meeting of the parties to the kyoto protocol FCCC/KP/CMP/2010/12/Add.1. Google Scholar


Velasco I. A., Torres D. V. (2019). El contexto geopolítico de la explotación forestal en la Península de Yucatán, México. Perspectiva Geográfica, 24(1), 116–137. Google Scholar


Vester H. F., Lawrence D., Eastman J. R., Turner B. L., Calmé S., Dickson R., Pozo C., Sangermano F. (2007). Land change in the southern yucatán and Calakmul biosphere reserve: Effects on habitat. Ecological Applications, 17(4), 989–1003. Google Scholar


Williams M. (2006). Deforesting the earth. From prehistory to global crisis. University of Chicago Press. Google Scholar
© The Author(s) 2022
Jovanka Špirić, Mariana Vallejo, and M. Isabel Ramírez "Impact of Productive Activities on Forest Cover Change in the Calakmul Biosphere Reserve Region: Evidence and Research Gaps," Tropical Conservation Science 15(1), (22 June 2022).
Published: 22 June 2022

land use
sustainable rural development
systematic review
Get copyright permission
Back to Top