Markedly divergent estimates of Amazon forest carbon density from ground plots and satellites

Aim The accurate mapping of forest carbon stocks is essential for understanding the global carbon cycle, for assessing emissions from deforestation, and for rational land-use planning. Remote sensing (RS) is currently the key tool for this purpose, but RS does not estimate vegetation biomass directly, and thus may miss significant spatial variations in forest structure. We test the stated accuracy of pantropical carbon maps using a large independent field dataset. Location Tropical forests of the Amazon basin. The permanent archive of the field plot data can be accessed at: http://dx.doi.org/10.5521/FORESTPLOTS.NET/2014_1 Methods Two recent pantropical RS maps of vegetation carbon are compared to a unique ground-plot dataset, involving tree measurements in 413 large inventory plots located in nine countries. The RS maps were compared directly to field plots, and kriging of the field data was used to allow area-based comparisons. Results The two RS carbon maps fail to capture the main gradient in Amazon forest carbon detected using 413 ground plots, from the densely wooded tall forests of the north-east, to the light-wooded, shorter forests of the south-west. The differences between plots and RS maps far exceed the uncertainties given in these studies, with whole regions over- or under-estimated by > 25%, whereas regional uncertainties for the maps were reported to be < 5%. Main conclusions Pantropical biomass maps are widely used by governments and by projects aiming to reduce deforestation using carbon offsets, but may have significant regional biases. Carbon-mapping techniques must be revised to account for the known ecological variation in tree wood density and allometry to create maps suitable for carbon accounting. The use of single relationships between tree canopy height and above-ground biomass inevitably yields large, spatially correlated errors. This presents a significant challenge to both the forest conservation and remote sensing communities, because neither wood density nor species assemblages can be reliably mapped from space.


INTRODUCTION
Amazonia contains half of all remaining tropical moist forest (Fritz et al., 2003). The total vegetation carbon storage of Amazon basin tropical forests has been subject to a wide range of estimates (Houghton et al., 2001;Malhi et al., 2006;Saatchi et al., 2007). These have varied from 58 Pg C (Olson et al., 1983) to 134 Pg C (Fearnside, 1997, scaled to whole basin), although there is now some general consensus in the middle of this range [e.g. 93 ± 23 Pg C (Malhi et al., 2006), 86 ± 17 Pg C (Saatchi et al., 2007) and 89 Pg C (FAO, 2010)]. However, these estimates of carbon stocks mask large differences at a smaller spatial scale, as local variations are cancelled out when summing over large areas: the spatial patterns visible in different maps of above-ground biomass (AGB) vary greatly, with little consistency even between studies that use similar methods and input data (Houghton et al., 2001).
It is of great importance that the distribution of carbon storage across the Amazon be well-characterized. Although there are many reasons that make it desirable to protect tropical forests, the protection of their carbon stocks and potential as a future carbon sink have made their preservation a current policy priority. A major initiative in international climate negotiations, Reducing Emissions from Deforestation and forest Degradation (REDD+), envisages payments in return for forest conservation. Though REDD+ is not yet operational, voluntary-sector afforestation/reforestation and REDD+ projects already exist, with REDD+ credit sales equal to $85 million  (Diaz et al., 2011). Country-to-country cash transfers have also taken place, with Norway leading the way, committing US$1 billion to the government of Indonesia, a similar amount to Brazil's Amazon Fund, and $250 million to Guyana, in return for their meeting goals for reducing rates of forest loss (Caravani et al., 2012). Other sources of conservation and development funding also assess projects based on their carbon impact: indeed, one of the stated criteria applied to all USAID funding (equivalent to US$40 billion in 2012) is to be carbonpositive where possible (U.S. Agency for International Development, 2012).
For a wide variety of conservation and sustainable forest management projects, forest carbon stocks -and changes in these stocks -must be estimated with confidence. Accurate estimation, however, still faces major challenges: indeed, in a comparison of estimates of carbon emissions from deforestation in the Amazon, the biggest cause of discrepancies between estimates was found to be due to carbon mapping, higher than the uncertainty in the mapping of deforestation (Gutierrez-Velez & Pontius, 2012). AGB is the largest carbon pool in most tropical forests, and also tends to be the best characterized because it is relatively easy to measure, with other carbon pools often estimated as a simple ratio of AGB (GOFC-GOLD, 2009).
Biomass maps of the Amazon region have been created in a number of ways. Some have used direct extrapolations from field-plot measurements, either multiplying the total area of forest by mean biomass density values (Olson et al., 1983;Fearnside, 1997;FAO, 2010) or by two-dimensional kriging (Malhi et al., 2006); others have used environmental gradients to co-krig field-plot measurements (U.S. Agency for International Development, 2012); and others have used remotesensing (RS) data (Saatchi et al., 2007). In the absence of continuous field measurements throughout an area of interest, RS datasets should provide the most accurate maps, because every location can be directly observed. Methods based solely on ground plots will only ever be able to sample a very small percentage of the total area, and due to access difficulties, a network of ground points will normally be biased towards more easily accessible regions (concentrated near rivers, roads and scientific field stations). However, using current technology AGB cannot be directly estimated from space (Woodhouse et al., 2012), and thus field plots remain essential for calibrating and validating RS maps. Ground-based estimates, and thereby calibrations of RS maps, are themselves limited by the small quantity of destructive biomass data available, which reduces the confidence in allometric equations used to convert ground data into estimates of AGB .
Two recent maps have been published that estimate AGB across the tropics at 1 km (Saatchi et al., 2011;subsequently called RS1) and 500 m (Baccini et al., 2012;RS2) resolution, aimed specifically at providing baseline data for REDD+, with the data being widely disseminated and used. Both maps use similar methods and datasets: they take millions of discrete 0.25-ha canopy height estimates from the Ice, Cloud and Land Elevation Satellite (ICESat) Geoscience Laser Altimeter System (GLAS) LiDAR sensor, convert these to estimates of AGB using empirically derived models that relate LiDAR variables to AGB using field plots located under some GLAS footprints, and use ancillary full-coverage RS layers to extrapolate these point AGB estimates across the landscape. The ancillary RS layers are visual and infra-red spectrum optical data from the Moderate Resolution Imaging Spectroradiometer (MODIS) sensors, elevation data from the Shuttle Radar Topography Mission (SRTM), and, in the case of RS1 only, QuikSCAT radar scatterometer data. The extrapolation of AGB is performed using multi-variable nonlinear models, MaxEnt in RS1 and RandomForests in RS2. Though they use similar input data, the nominal date of the resulting AGB maps differs between the two, with RS1 dated as 'early 2000s' , and RS2 2007'early 2000s' , and RS2 -2008. RS1 provides a continuous uncertainty map, giving an uncertainty of ± 6% to ± 53% associated with every pixel, and assumes these errors are spatially uncorrelated to give an uncertainty for the total carbon stock for Amazonia of < ± 1% (Saatchi et al., 2011). RS2 does not provide a pixel-level uncertainty map but instead held back some training data, using a Monte Carlo approach to estimate uncertainty at the level of Amazonia as ± 7% (Baccini et al., 2012).
In both cases, the primary calibration data used to produce the maps is derived from profiles of tree height from the ICESat GLAS sensor. Although these data do include some information about the structural characteristics of the forest within the LiDAR footprints, canopy height is the principal parameter detected (Lefsky et al., 2005). However, allometric equations that relate physical attributes of trees to their above-ground biomass normally rely on three parameters: in addition to tree height (H), tree diameter at 1.3 m (D) and wood density (ρ) are very important (Chave et al., 2005), and mean values and ratios between these parameters vary significantly between regions (Chave et al., 2005;Feldpausch et al., 2012;Quesada et al., 2012), associated with different species communities (ter Steege et al., 2006). We know that wood density increases from west to east across Amazonia (Baker et al., 2004;ter Steege et al., 2006), inversely correlated to stem turnover rate (Quesada et al., 2012). This gradient is driven by soil fertility, notably total soil phosphorus and the concentration of exchangeable potassium ions (Aragão et al., 2009), and especially by the physical qualities of the soil. Thus, the fertile but shallower soils of the western Amazon lead to higher productivity and faster turnover, and a set of species with low wood density; conversely, the low fertility but deep and freely-draining soils of the eastern Amazon tend to have lower productivity and slower turnover, and species with much higher wood density. The relationship between diameter and height also varies across the basin, but with more complexity than wood density, mostly related to climatic factors (Feldpausch et al., 2011). These are approximated into four zones (Feldpausch et al., 2011, with the use of a different D:H model in each zone, greatly reducing the error in the prediction of H from D compared to a pan-Amazonian model . Thus, although D, ρ and H were used in the field-plot calibration of RS1, and D and ρ for RS2 (with the allometric  Chave et al., 2005), regional differences in D:H ratios and ρ are not detected by GLAS, and thus the continental-scale GLAS-AGB calibrations used could smooth out these differences. This is likely to result in significantly higher regional uncertainties than estimated by Saatchi et al. (2011) or Baccini et al. (2012).
In order to test this, we use a unique dataset of 413 field plots located throughout tropical South America, compiled as part of RAINFOR (Red Amazónica de Inventarios Forestales; Amazon Forest Inventory Network; Malhi et al., 2002), the Amazon Tree Diversity Network (ter Steege et al., 2003), TEAM (Tropical Ecology Assessment and Monitoring) and PPBio (Brazilian Program for Biodiversity Research) (Fig. 1). Data in these plots were collected using a consistent methodology, and AGB was calculated using a T-SQL query to a single database. We compare these field plots directly to the two remote-sensing-derived maps, and additionally create a plotbased AGB map using simple two-dimensional kriging (K DHρ) to allow a spatial comparison.

MATERIALS AND METHODS
Details of field methods and error checking procedures involved in the RAINFOR permanent plot network are discussed in detail elsewhere (Phillips et al., 2008(Phillips et al., , 2009a. The individual stem data for every plot used in this study are held in a database (http://www.forestplots.net/), which allowed us to calculate plot-level AGB consistently with a single T-SQL query . The TEAM plots were downloaded and added to the database in April 2013, with data set identifier codes of 20130415013221_3991 and 20130405063033_1587. We only used plots where data were available for every stem and trees had been measured consistently above buttresses. Plots above 1000 m elevation were excluded, as were plots in nonforest ecosystems. On average across plots, 77% of stems were identified to the species level, and 92% to the genus level. The dates at which the plots were most recently measured, and the number of times they had been re-censused, varied: in order to dampen the influence of short-term disturbances and to produce values that most closely represented the landscape AGB distribution, the value for each plot was calculated as the mean of all census values, weighted by census interval lengths before and after each measurement. Censuses collected from 2010 onwards were excluded as these post-date the remote-sensing data, apart from 41 plots that were only measured for the first time during or after 2010, in which case the earliest available census was used.
The principal AGB dataset was calculated using the threeparameter moist tropical forest model from Chave et al. (2005), with height estimated from d.b.h. individually for each stem using the region-specific Weibull models from Feldpausch et al. (2012), and wood density values estimated for each stem using the mean value for the species in the Global Wood Density Database Zanne et al., 2009), or the mean for the genus using congeneric taxa from Mexico, Central America and tropical South America if no data were available for that species (K DHρ). For comparison, AGB was also calculated using the same allometric equation but with the pan-Amazon Weibull model from Feldpausch et al. (2012) (KDρ), regional height models but with a dataset mean wood density value of 0.63 applied to every stem (KDH), and with the pan-Amazonian height model and mean wood density applied to every stem (KD).
In order to compare the AGB dataset directly with the field plots, we averaged the field plots within 20 km × 20 km boxes and compared the mean value for these boxes to the mean AGB of RS1 and RS2. This was intended to reduce the noise involved in comparing single field plots to their surrounding remotesensing pixel. This resulted in comparisons being made with 107 unique points, with a mean of 3.9 field plots in each (range 1-14). We attempted to produce the kriged maps using universal kriging (ter Steege et al., 2003), but this proved impossible because of high local variation in AGB values of neighbouring plots, resulting in little spatial autocorrelation. Plots located within a 250-m search radius were averaged, which reduced the total number of independent points entering the kriging procedure from 413 to 378; this assisted matters, but a semivariogram showed that there was still little spatial autocorrelation in the dataset (Fig. S1). We therefore used an inverse distance kernel with a smoothing distance of 100 km, which removed local variation and produced output layers showing the broad spatial trends in the dataset. The output kriged maps were produced at a 500-m resolution using the MODIS sinusoidal projection, an equal-area projection used in the creation of RS2.
RS1 was provided by S. Saatchi (NASA Jet Propulsion Laboratory, CA, USA) in a geographic projection with a pixel size of 0.00833°; RS2 was provided by A. Baccini (Woods Hole Research Center, MA, USA) in a MODIS sinusoidal projection at 500 m resolution. RS1 was warped to the projection of RS2 using an exact mathematical transformation. Pixel values were assigned during warping using the 'nearest neighbour' algorithm, so no pixel values were changed by the warping procedure.
The units of the maps were in tonnes of biomass per hectare (Mg ha −1 ). Total carbon stocks for subsets of the resulting layers were calculated by multiplying the mean biomass of a subset by its area in hectares, and then converting biomass to carbon by multiplying the result by 0.5 (as dry biomass is assumed to be 50% carbon; Penman et al., 2003).
All the plots entering the kriged map were located in forest areas with no recent anthropogenic disturbance, but a significant proportion of Amazonia is non-forest or degraded forest (Fig. 1a). Unsurprisingly, KDHρ overpredicted AGB in all areas dominated by non-forest land-cover types compared to the RS maps. Therefore the maps are most comparable in undisturbed forest areas, so all comparisons were performed in Intact Forest Landscape (IFL) (Potapov et al., 2008) areas only, with the exception of the analysis of recent deforestation. IFLs are defined as forest areas minimally influenced by human economic activity, with an area of at least 50,000 ha and a minimum width of 10 km. The IFL layers are kept updated for new infrastructure, settlements or commercial activities by their developers using a combination of field data and remote-sensing data (Potapov et al., 2008).

RESULTS AND DISCUSSION
The field plots with our best estimate of AGB (P DHρ) show a robust trend of increasing AGB with increasing latitude, longitude and distance along a SW-NE line (Fig. 2a-c; the parameters of the best-fit lines are given in Table S1; input plot biomass data are available in Lopez-Gonzalez et al., 2014). The kriged map of the same field plots (Fig. 3c) shows that the latitudinal and longitudinal trends seen in the graphs are clearly driven by the dominant SW-NE gradient. By contrast, the remote-sensing layers RS1 and RS2 show significant decreasing trends with dis-tance along a SW-NE line (Fig. 2c, Table S1). Subtracting the two RS layers from the plot AGB values emphasizes the trends described above, with positive differences (i.e. RS1 and RS2 greater than P DHρ) in the south and west, and negative differences in the north and east (Fig. 2d-f, Table S1).
Two-dimensional kriging of the plot dataset (KDHρ) allows area-based comparisons to be made between the field-plot and RS datasets. The total Amazon basin AGB stocks in RS1, RS2 and KDHρ did not differ greatly for intact forest landscape (IFL) areas (Potapov et al., 2008) (Table 1), with KDHρ and RS2 having very similar total stocks, and the RS1 estimate being 11% lower. The patterns of AGB differ greatly among the maps, however, as shown in Fig. 3 and demonstrated by the high root mean squared error (RMSE) values comparing RS1 and RS2 to KDHρ ( Table 1). The two RS maps do not show the strong SW-NE AGB gradient seen in KDHρ (Figs 2 & 3). RS1 shows similar AGB in western and eastern Amazon forests, with distinctly lower AGB in central Amazonia than either of the other maps, explaining its lower total stock estimate. RS2 has less variation in AGB overall, but with the highest values in the central-western Amazon, opposite to the pattern seen in the KDHρ map.
We believe that the AGB gradient in the field plots cannot be an artefact of our analysis: the ground-based estimates use consistent field measurements (Phillips et al., 2008(Phillips et al., , 2009a in wellsurveyed plots, with AGB calculated at a stem level using a trusted allometric equation (Chave et al., 2005) involving tree diameter, wood density and height. We are confident that diameters are measured to high precision, as a primary purpose of these plots is to track small changes in diameter through time; we are confident that our wood density values are accurate due to careful species identification and the use of a reliable wooddensity dataset Zanne et al., 2009); and we account for spatial variation in stem height (Feldpausch et al., 2011). While K DHρ is clearly not an accurate spatial map, being based solely on 413 point measurements, these are well distributed across the study area and thus should correctly display broad regional trends in forest structure: every IFL pixel in Amazonia is within 500 km of at least eight plots (Fig. 1b). A semivariogram analysis of the field data shows that the spatial autocorrelation of plots does not start to decrease until they are about 700 km apart, suggesting this plot network is sufficient to represent the potential AGB of old-growth forests across the whole basin (Fig. S1).
It is clear that the use of RS1 or RS2 for carbon accounting purposes for a subset of this area will produce very different results from those using K DHρ: the RS maps will underestimate stocks in the Guiana Shield and overestimate in SW Amazonia (Table 1). To demonstrate the difference for a relevant example, we calculated the estimated emissions from deforestation in Brazil from 2009-2011, after the reported date of either RS map, using the PRODES dataset (INPE, 2012). We found significantly higher carbon estimates with KDHρ than with either RS map (Table 2). It is possible that estimates from the RS maps are lower because these areas were already degraded at the time the maps were made, with this perhaps explaining the lower value for RS2 than RS1, as RS2 is produced for a date c. 5 years later than RS1. However, this is unlikely to be the case in all areas, and thus cannot explain the extent of the difference.
It is important to understand the drivers of the AGB gradient seen in the field plots. From an ecological point of view, AGB is ultimately a function of net primary production (NPP) and the turnover rate of the forest. Spatial differences in NPP and turnover rates are associated with different species with different life-history strategies and structures caused by different climatic conditions and the chemical and physical properties of the soil (Quesada et al., 2012), with these different floristic communities associated with different AGB values. The key ecological parameters associated with differing AGB are basal area, wood density and D:H ratios, all of which vary across the basin (Baker et al., 2004;ter Steege et al., 2006;Banin et al., 2012;Feldpausch et al., 2012;Quesada et al., 2012), but none of which is directly detected by RS. Mapping basal area and wood density from the plots shows that both increase from SW-NE, though wood density shows a larger proportional trend than basal area (Fig. 4a,c). It is also known that, in general, tropical South American trees are shorter for a given diameter than trees from other tropical regions (Banin et al., 2012), with the exception of the Guiana Shield where trees are comparatively tall for a given diameter, with D:H relationships statistically indistinguishable from the forests of Africa and Southeast Asia (Feldpausch et al., 2011). In order to assess the relative impact of wood density and tree height on AGB, we recalculated the AGB values of the 413 field plots using the same three-parameter allometric equations and diameter information, but applying three different approaches to the other two variables: 1 K Dρ: Using a pan-Amazonian D:H model rather than the four regional height models , but the same wood density values as KDHρ; 2 KDH: Using a constant value of 0.63 as the wood density for every stem, but the regional height models as in KDHρ; 3 KD: Using a pan-Amazonian D:H model and a constant wood density value, but the same allometric equations, so AGB varied between plots solely due to D.
KDρ and KDH both have significant SW-NE AGB gradients, albeit less marked than for KDHρ (Fig. 4). On average across the Amazon, the exclusion of wood density (KDH) leads to a small reduction in predicted AGB compared to KDHρ, but this reduction is bigger when considering only the Guiana Shield (known to have high wood density), and is reversed in SW Amazonia (known to have lower woody density) (Fig. 4, Table 1). Using a pan-Amazonian height model (KDρ) leads to a very small reduction in overall predicted AGB across the Amazon, with a decrease in the Guiana Shield, and a matching increase in SW Amazonia. Excluding both height and wood density (KD) again results in an small reduction in predicted AGB for the whole basin, with a very large underestimate in the Guiana Shield (−17.2%), and a smaller overestimate in SW Amazonia (12.5%) (Fig. 4, Table 1). From this analysis, we conclude that the RS layers underestimate AGB in the Guiana Shield due to a contribution of using mean wood density (an underestimate) and a generic pan-Amazonian relationship between diameter and height (ignoring the fact that trees are taller than would be expected for a given diameter in this region), with the two factors having approximately equal contributions. In SW Amazonia, the difference is caused by the same two factors in the opposite direction: using pan-Amazonian wood density and D:H relationships here results in an overestimate of AGB. In SW Amazonia the two factors are not equal in magnitude, with wood density causing approximately three times more overestimation than the D:H relationship (Table 1). Wood density and D:H relationships alone, however, cannot explain all the differences between RS1/RS2 and K DHρ. In both the Guiana Shield and the SW Amazon, the difference between KDHρ and KD is smaller than the difference between KDHρ and the RS maps. The unexplained difference is over 10% for the Guiana Shield, and 3-5% for the SW Amazon. There must therefore either be further factors in the processing chains involved in developing RS1 and RS2 from their input datasets that contribute to the over-and under-estimation in these regions, or the non-random nature of the input field datasets must be causing this additional difference. We believe the latter explanation is unlikely, as any bias towards pristine forests would tend to cause an overestimate in the plot-based estimate, but instead the field plots estimate lower AGB in SW Amazonia. Possible explanations for the former include incorrect or saturating relationships between GLAS footprints and AGB, or explanatory variables not fully capturing the spatial variability in forest structure, causing the resulting maps to tend towards the mean. The differences between RS1 and RS2 themselves are caused in part by the use of different remotesensing datasets, different methods of processing the GLAS data, and different extrapolation approaches, but also by the choice of allometric equation to convert their field plot data into AGB estimates. RS2 uses a two-parameter equation excluding height, whereas RS1 uses the three-parameter equation we used to estimate AGB from our plots, albeit with effectively a pan-Amazonian D:H relationship. The equation excluding height used in RS2 is known to estimate higher AGB values than the three-parameter equation used in RS1 (Chave et al., 2005;Feldpausch et al., 2012), so this choice probably explains much of the 12% higher total AGB estimate for Amazonia by RS2 compared to RS1 (Table 1).  (Baccini et al., 2012); (c) kriged map of AGB from field plots, with AGB calculated using diameter, species-specific wood density, and a regional height model (KDHρ), showing only areas identified as intact forest landscapes (IFL); (d) difference between RS1 and KDHρ; (e) difference between RS2 and KDHρ; (f) difference between RS1 and RS2. Difference maps have non-IFL areas masked out. The projection is sinusoidal, an equal-area projection.

CONCLUSIONS
The two remote-sensing maps, RS1 (Saatchi et al., 2011) and RS2 (Baccini et al., 2012), show very different spatial patterns of AGB distribution across Amazonia, compared to each other and compared to field plots distributed across the region (Figs 2 &  3). In particular, the strong gradient of increasing AGB from SW to NE Amazonia that we observe in the field data is not replicated in the RS datasets. RS1 and RS2 do have associated uncertainty estimates, but the differences observed between the maps and field plots considerably exceed the reported uncertainties over Amazonia in both cases. Our analysis shows that this is mostly due to neither study accounting for the known regional variations in wood density and D:H relationships. Specifically, they do not use any spatial layers corresponding to wood density, and use only continental (Saatchi et al., 2011) or global (Baccini et al., 2012) relationships between ICESat GLAS waveforms and AGB. We are not advocating the use of extrapolated AGB maps derived from sparse field measurements for carbon accounting: we firmly believe that AGB is best mapped using a combination of RS data calibrated and validated using a substantial number of carefully established field plots. It is this step of careful validation against best estimates from scientific field plots that we believe was lacking in the RS studies. Looking forward, we provide the following recommendations to improve AGB estimates. First, regional differences in wood density and D:H relationships must be considered when mapping AGB. One universal algorithm predicting AGB from a suite of remotesensing variables is not appropriate, as wood density cannot be detected from space, and the structural parameters of forests cannot yet be reliably extracted from RS data. Different algorithms should be applied to different regions, potentially based on maps of soil type or vegetation structure. Alternatively spatially explicit maps of wood density and diameter:height relationships should be directly incorporated into biomass mapping Table 1 Comparison of the mean above-ground biomass (AGB) and total above-ground carbon stock contained in two remote-sensing-derived maps of the Amazon forests (RS1, Saatchi et al., 2011;RS2, Baccini et al., 2012) with a map derived from kriging 413 field plots (KDHρ), and maps derived from these same field plots but excluding wood density, local tree height allometry, or both (KDH, KDρ and KD, respectively). In all cases, only intact forests are considered (Potapov et al., 2008). RMSE, root mean squared error, is calculated on a 500 m pixel basis.   (Asner et al., 2012). There is a clear need for the ecological community to provide regional and pantropical maps of basal-area-weighted wood density based on plot data, potentially extrapolated using climate or other layers, as inputs for the biomass mapping communities. Second, our study demonstrates the importance of creating and sustaining large networks of field plots. This analysis was only possible because a sufficient number of plots have been located across the basin using a standard methodology, with the data included in a single database allowing identical processing chains to be applied to stem data. It is important that such networks are maintained and improved across the tropics, and vital that current spatial data gaps are filled (Fig. 1b). Third, measuring tree height and identifying the thousands of Amazon tree species (at least to genus level, enabling stems to be matched to wood density information), were essential components of the field data. Recording tree diameters alone would not have allowed us to identify these important regional gradients in AGB: variation in biodiversity can matter greatly for determining carbon stocks.  The unpublished field data summarized here involve contributions from numerous field assistants and rural communities in Bolivia, Brazil, Colombia, Ecuador, French Guiana, Guyana, Peru, Suriname and Venezuela, most of whom have been specifically acknowledged in Phillips et al. (2009b). We also thank Edmar Almeida de Oliveira, Vega Arenas, Antonio Peña Cruz, Camilo Diaz, Javier Silva Espejo, Leandro Ferreira, Luis Valenzuela Gamarra, Julio Iriaca, Eliana Jiménez, Diego Rojas Landivar, Carolina Levis, Rodolfo Vásquez Martínez, Maria Cristina Peñuela, Irina Mendoza Polo, Ednodio Quintero, Agustin Rudas, Paulo Sérgio Morandi, Natalino Silva, Hugo Vásquez, and Jaim Ybarnegaray for their invaluable contributions. We thank Sue Grahame and Georgia Pickavance for their support with the ForestPlots.net database and Joana Ricardo for work supporting RAINFOR collaborators. We dedicate this work to the memory of Alwyn Gentry, Jean Pierre Veillon, Samuel Almeida and Sandra Patiño, whose pioneering efforts to understand Neotropical forest composition and structure from the ground up have been an inspiration for succeeding generations of ecologists.

SUPPORTING INFORMATION
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Figure S1
Semivariogram showing how variance between biomass values for the field plots varies with distance. Table S1 Parameters for the fits in Figure 2. The permanent archive of the field plot data can be accessed at: http://dx.doi.org/10.5521/FORESTPLOTS.NET/2014_1 Divergent forest carbon maps from plots & space BIOSKETCH Edward Mitchard is a research fellow at the University of Edinburgh, specializing in the remote sensing of tropical ecosystems. His main research focus is the development of systems for quantifying changes in above-ground biomass for avoided deforestation projects, and the estimation of uncertainty in such systems. He is also interested in the environmental and anthropogenic drivers of ecological gradients, in particular in terms of woody cover and biomass, and studies these using ground and remote sensing data across tropical forests and forest-savanna boundaries. This has also led him to research the extent and causality of woody encroachment. RAINFOR was set up by Oliver Phillips, Yadvinder Malhi, and Jon Lloyd in 2000, and has evolved into a very large international collaboration involving hundreds of scientists from across South America, providing the main source of information on the long-term dynamics of Amazonia's forest. RAINFOR has led to many scientific discoveries, including the first quantification of the carbon sink in intact tropical forest. The framework is centred on a set of permanent forest plots, repeatedly censused using a common inventory system with trees identified to an excellent level of taxonomic detail, and associated with soil and plant biogeochemical data.