Abstract
Purpose of Review
This review presents cutting-edge methods and current and forthcoming satellite remote sensing technologies to map aboveground biomass (AGB).
Recent Findings
The monitoring of carbon stored in living AGB of forest is of key importance to understand the global carbon cycle and for the functioning of international economic mechanisms aiming to protect and enhance forest carbon stocks. The main challenge of monitoring AGB lies in the difficulty of obtaining field measurements and allometric models in several parts of the world due to geographical remoteness, lack of capacity, data paucity or armed conflicts. Space-borne remote sensing in combination with ground measurements is the most cost-efficient technology to undertake the monitoring of AGB.
Summary
These approaches face several challenges: lack of ground data for calibration/validation purposes, signal saturation in high AGB, coverage of the sensor, cloud cover persistence or complex signal retrieval due to topography. New space-borne sensors to be launched in the coming years will allow accurate measurements of AGB in high biomass forests (>200 t ha−1) for the first time across large areas.
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Introduction
Forests cover approximately 30% percent of the global land surface and play a key role in the global carbon cycle. The world’s forests store approximately 45% of terrestrial carbon [1]. Most of this carbon is stored in trees in the form of AGB through the process of photosynthesis. AGB includes all vegetation above the ground (i.e. stems, branches, bark, seeds, flowers and foliage of live plants) and approximately 50% of its composition is carbon [2]. AGB is usually measured in metric tons of dry matter per hectare (e.g. t ha−1 or Mg ha−1) or in metric tons of carbon per hectare (e.g. t C ha−1 or Mg C ha−1).
Intergovernmental organisations and international agreements such as the United Nations Framework Convention on Climate Change (UNFCCC) in 1992 and its extension in 1997 with the Kyoto Protocol have recognised the importance of monitoring and reducing the amount of greenhouse gases (GHG) emitted to the atmosphere from anthropogenic activities. During the 21st Conference of Parties of the UNFCCC in 2015, the first comprehensive climate agreement (Paris Agreement) was achieved, for which the parties aim to hold the increase in the global average temperature to below 2 °C and to pursue efforts to limit the temperature increase to 1.5 °C. Carbon dioxide (CO2) is one of the most significant trace gases, which can alter global biogeochemical cycles such as the global carbon cycle. The heating derived from the increase of CO2 in the atmosphere can also produce changes in weather patterns [3]. In most tropical countries, deforestation is the main source of CO2 from terrestrial ecosystems and the second largest anthropogenic source after fossil fuel combustion [4].
The global monitoring of forest AGB is essential to understand the carbon cycle and to reduce carbon emissions. However, its amount and spatial distribution is still uncertain due to the difficulties in measuring AGB at the field scale [5]. Remote sensing techniques, especially space-borne sensors, collect data correlated to the spatial distribution of AGB across large regions, nationally and even globally, in a cost-efficient manner [6, 7]. Aside from a long series of passive optical remote sensors, researchers and practitioners can also use active sensors such as Synthetic Aperture Radar (SAR) and Light Detection and Ranging (LiDAR).
Global and regional biophysical forest parameter maps such as forest area, canopy cover, growing stock volume (GSV), AGB and canopy height can be generated using remote sensing techniques with spatial resolutions in the range of 25 m to 1 km (e.g. [8, 9,10,11,12,13,14, 15••, 16, 17•, 18,19,20,21]). However, these approaches face challenges related to the absence of well-distributed in situ data for calibration at scales useful for remote sensing [22] and the limited sensitivity of satellite sensors to AGB [23]. Each satellite sensor has different strengths and weaknesses related to spatial resolution, sensor technology, number of spectral bands, revisit times and cost. In this review, operational and imminent remote sensing technologies with a focus on space-borne sensors are presented together with current state-of-the-art approaches to estimate carbon stocks in forest AGB.
In Situ Data
AGB is measured accurately and directly by destructive in situ sampling methods. This is a laborious, expensive and impractical approach for large scales [24]. Non-destructive in situ methods such as forest inventories make use of allometric models to predict AGB. Forest inventories are broadly used for AGB monitoring as their accuracy lies between 2 and 20% [25]. Biophysical parameters like tree height and diameter at breast height (DBH) are commonly measured in forest inventories and related scientific studies and are used to estimate AGB from allometric equations. Some countries have also developed modelling approaches based on forest stand variables such as tree species, site indices and ecological regions to predict AGB across wide areas [26]. Most forest inventories were developed to estimate commercial growing stock volume of stems, neglecting other biomass components like branches and leaves. Biomass expansion factors (BEFs) are used to convert growing stock into non-inventoried tree components. The use of BEFs involves a two-step process, stem volume estimation followed by the application of the expansion factors. Therefore, allometric equations are preferred over BEFs as the calculation is limited to one step, reducing the error propagation in the process.
As the field samples used to create allometric models are delimited to the study area, their applicability is usually restricted to specific species and sites [27,28,29,30]. Allometry varies with climatic conditions, vegetation structure, tree species and growth-form of trees [31,32,33], and therefore different forest biomes and even regions within biomes will show variations in allometry. The selection of appropriate equations is a crucial step when using allometry as a method. An inappropriate choice of allometric model can become the most important error source in the estimation of AGB [34]. These errors are mostly a consequence of using allometric equations outside the diameter range [34] or in a different area [35] from which those equations were developed. The small sample of tree measurements commonly used to generate these models can result in uncertainties ranging from −4 to +193% [36]. Important variations obtained in C stock have been found, with overestimations of up to 93% when using different biomass allometric equations in the same study area [37].
Several international consortia such as AfriTRON [38], RAINFOR [39], ForestPlots [40] and CTFS-ForestGEO [41] aim to coordinate long-term monitoring of forest plots. They have established permanent sample plot networks across tropical forests using robust protocols for measurements and continuous monitoring of plots and created databases to be used in ecological studies. These plot networks are essential for calibrating and monitoring remote sensing approaches in tropical forest areas.
In temperate and boreal forested areas, there is good availability of forest inventory ground data as well as allometric equations [42]. Unfortunately, these data are unavailable in many developing countries in tropical regions with large areas of natural forests due to the geographical remoteness, lack of capacity, data paucity or armed conflicts. The Congo Basin is a clear example of the scarcity of ground samples. Even though the Congo basin is one of the largest forested areas in the world, only a small number of plots has been measured and few allometric equations have been developed for the forests of this region [43]. As a result, data availability and subsequently allometric models are the key limiting factors for quantifying AGB. Methods based on or assisted by remote sensing technology aiming to estimate forest biomass over large scales (i.e. global, biome and continental levels) should focus on developing methods which can be applied in areas with data availability problems while accounting for regional variability.
Capabilities and Limitations of Earth Observation Data
Before the introduction of remote sensing technologies, several approaches were used to produce AGB maps. The most well-known, simple and fast is the biome-average approach. The biome-averages are single values of biomass per unit area (e.g. t ha−1). These biome-averages are applied to broad forest types or biomes and have been mostly calculated and updated from analyses of country-level carbon stock data archived by the United Nations Food and Agricultural Organization (FAO). Unfortunately, estimates based on national forest inventories from some developing countries are not always reliable. Additionally, the different sampling designs used by those inventories are not taken into consideration when estimating these values, which might lead to large uncertainties and biases. However, the main advantage of using biome-averages is that the values are readily available at no cost, hence becoming the simplest starting point for a country to assess the relative amount of carbon stocks [4].
Three broad types of remote sensors on board of Earth observation platforms are generally used to map AGB: passive optical, LiDAR and microwave. Each type of sensor has different characteristics which make them suitable for monitoring forest vegetation. Passive sensors use the reflected sunlight emitted by the sun to obtain measurements, while active sensors generate their own signal, which is reflected, refracted or scattered from the Earth’s surface before being received by the sensor. The correlation between the signal received by any type of sensor and AGB can present regional variations due to factors such as forest structure, species composition and wood density, allometry, atmospheric effects and vegetation moisture (e.g. [44, 15••]).
Passive Optical
Vegetation indices estimated through passive optical imagery (e.g. leaf area index, normalised difference vegetation index) are most sensitive to the photosynthetic parts of vegetation [45]. As a result, those indices are also indirectly related to AGB by means of an empirical relationship between foliage and total AGB. The signal from optical sensors is therefore sensitive to variations in canopy structure, and several methods use this relationship to model AGB across the landscape [4, 46]. This relationship involves a certain amount of error as the AGB of vegetation is mostly composed of non-photosynthetic parts.
Optical sensors have great advantages for global vegetation monitoring. The incident electromagnetic radiation that is not absorbed or scattered by the atmosphere can be absorbed, transmitted or reflected by the vegetation. The reflected radiation from the targets is measured by the remote sensor. Vegetation causes diffuse reflection due to its roughness and can be easily differentiated from other surfaces due to chlorophyll causing reflectance in the visible green light spectra and strong reflectance in the near-infrared, as well as absorption in the red and blue sections of the visible spectrum [45].
A multispectral sensor usually has between 3 and 10 broad bands, while hyperspectral sensors have hundreds to thousands of narrow bands. Some studies have used a hyperspectral satellite to map AGB over small areas (e.g. [47, 48]), but this is challenging for large areas due to processing requirements and the reduced number of hyperspectral satellites.
Optical sensors have been operating for a long time and rich data archives are available for studying vegetation dynamics. For example, the Landsat and NOAA AVHRR missions have acquired observations over the last 40 years. Another advantage of optical sensors is that their high to coarse resolution imagery can usually be obtained for free or at low cost. The main shortcoming of optical imagery is cloud cover obscuring the observations of the land surface. This is not crucial in boreal or temperate latitudes, but can be a problem in tropical areas where only a few days in a year are cloud-free. Moreover, as passive sensors, they can only collect meaningful imagery during daylight, which reduces the number of potential revisit times in comparison with active sensors like SAR or LiDAR. Thus, the chances to obtain a cloud-free image are lowered.
Several studies have mapped AGB calibrating the algorithm with field observations and using high to coarse resolution multispectral optical imagery to upscale the measurements over the landscape (e.g. [49, 14, 11, 50]). The use of high-resolution sensors is usually restricted to small areas due to acquisition costs, revisiting times and the large volume of data needed to cover extensive areas. Coarse resolution sensors such as MODIS have a 24-h revisiting time in comparison with moderate resolution sensors such as Landsat with a 16-day revisiting pass. As a result, coarse resolution optical sensors have more chances to have cloud-free observations. It should be noted that in partly cloudy conditions, there is a chance of cloud contamination in a coarse resolution pixel where a moderate or high-resolution sensor might capture both cloudy and cloud-free pixels over the same area. Multi-temporal radiometrically consistent cloud-free datasets can be generated by high and moderate resolution sensors, but it can be technically demanding and time-consuming [49, 51]. The rapid development of high performance computer facilities (HPC) and cloud computing (e.g. Google Earth Engine) currently allows the generation of such datasets at moderate resolutions for large areas [52, 53••, 54]. The revisiting time of moderate resolution sensors is also improving with new operational programmes such as Sentinel-2, which with two satellites operating simultaneously (2A and 2B), will reduce potential repeat coverage to 5 days between acquisitions over equatorial regions and up to 2 days over regions in higher latitudes.
Most hyperspectral approaches focus on the retrieval of vegetation indices that can be correlated to forest biochemical parameters and leaf area index (LAI) [55,56,57]. Using Hyperion data, le Maire et al. [58] was able to estimate canopy leaf biomass. However, the poor relationship between stem biomass and vegetation indices has been indicated by some studies [59, 60]. Nevertheless, the use of hyperspectral data in combination with other sensors can improve AGB estimations as shown by Lucas et al. [61] and Swatantran et al. [60]. Hyperspectral remote sensing has the potential to improve biomass mapping by providing information on vegetation health and species composition.
Optical imagery is therefore suitable for forest area mensuration, vegetation health monitoring and forest classification, but presents limited correlation with forest AGB after canopy closure. Estimation of AGB by optical sensors has to deal with a saturation of the signal retrieval at low AGB stocks due to canopy closure [4]. However, recent studies suggest that there is correlation of optical imagery (Landsat, MODIS) to AGB beyond the theoretical saturation, especially in infrared bands [13, 62, 63] which are sensitive to shadowing and moisture differences.
Light Detection and Ranging—LiDAR
LiDAR is a technology consisting of active optical sensors which transmit laser pulses to targets in order to measure distances. LiDAR remote sensing systems can be classified according to the platform in which they are mounted (space-borne, airborne, ground-based or hand-held), the type of returned signal (discrete return or full waveform), the scanning pattern (profiling or imaging) and the footprint size (<1 m diameter small footprint, 10–30 m diameter medium footprint and >50 m diameter large footprint). A LiDAR footprint is an area illuminated by the laser and from which the waveform-return signal gives information.
Because LiDAR sensors retrieve canopy height from the distance measurements between the sensor and the target, they are not limited by the same signal saturation for the estimation of AGB as optical and radar sensors, which correlate AGB with spectral reflectance or radar backscatter signals. A high LiDAR point density allows for more ground returns to be obtained through gaps in the canopy. In particular, airborne and ground-based imaging LiDARs provide direct and very accurate measurements of canopy height. However, the use of airborne and terrestrial platforms would be excessively expensive for continental and global scale mapping. The only space-borne LiDAR sensor to date was the Geoscience Laser Altimeter System (GLAS) instrument aboard the NASA Ice, Cloud and land Elevation Satellite (ICESat). ICESat scanned the globe from 2003 to 2010 following a footprint profiling pattern along the orbit and produced a global coverage of full waveform signal large footprints (approximately 65 m in diameter). ICESat sampled millions of such footprints every 172 m along the track. This sensor did not generate images but provided full-wavelength point information that could be used after processing for calibration purposes. Canopy height can be calculated based on the relative time elapsed between the energy reflected from the top of the canopy and the ground (waveforms) [64]. However, GLAS waveforms have problems estimating canopy height over sloped terrain [65].
Several authors have studied LiDAR-derived biophysical canopy metrics to characterise forest vertical structure [12, 66,67,68,69,70,71]. Allometric models can then be used with those metrics to estimate AGB. AGB estimated using the large-footprint GLAS sensor has been widely used for calibration/validations purposes, especially in areas with poor field data availability. These LiDAR space-borne sensors cannot be used alone to produce wide area AGB mapping, but they are very useful in combination with other Earth Observation datasets (e.g. [13, 15••]). There is no LiDAR satellite in orbit at the present time, but some are in the development stage.
Microwave
Microwave earth observation sensors use the electromagnetic radiation in the microwave wavelength range to provide information about the planet’s land, ocean and atmosphere. Microwave sensors used in forest biomass studies are either passive microwave radiometers which measure the natural microwave emission from earth or active radar altimeters which transmit microwaves and receive a backscattered signal from a surface. However, few studies have explored the use of passive microwave radiometers to estimate forest AGB [72••, 73]. The very coarse spatial resolution allowed by these radiometers (>10 km) makes the calibration and validation of these approaches difficult and only useful for global scale studies.
Most studies use a type of active radar called SAR which is able to acquire high and moderate resolution imagery. SAR is a side-looking active radar system. The backscattered signal contains both an intensity and a phase component. The intensity is a measure of the strength of the returned signal and is affected by geometric and dielectric properties (essentially the moisture content) of the surface. The phase describes the phase angle of the returned radar echo, and it is a combination of hundreds of interactions with individual scattering objects within a target area. Microwave wavelengths allow imaging of the land surface through cloud cover, and with SAR being an active system, images can also be gathered at night. Airborne or space-borne SAR systems follow a side-looking design that uses the Doppler effect of relative motion between the antenna and its target to provide distinctive long-term coherent signal variations to generate much higher resolution imagery than would be possible from a real aperture radar [74].
There are three fundamental physical scattering mechanisms by which a microwave pulse is scattered. These are volume scattering, double bounce and rough surface (or ‘Bragg’) scattering [75]. Double-bounce scattering occurs when the signal is reflected from two or three orthogonal surfaces with different dielectric constants, directly back to the sensor. This is common from man-made surfaces, such as in urban environments. Naturally occurring surfaces that cause double-bounce backscattering include vertical tree trunks, particularly those in still water as found in mangrove swamps. Volume or canopy scattering is produced from a cloud of randomly oriented dipoles [75] typically seen in leaf and branch interactions in forest canopies. Scattering from a rough surface results in Bragg scattering, with the signal being scattered in multiple directions. Scattering from still water results in very low signal intensity, as most of the signal is reflected away from the sensor.
Transmitted radar pulses are polarised electromagnetic waves in either the horizontal (H) or vertical (V) plane, and the returned signal can also be received in either the horizontal or vertical plane. Co-polarised SAR data (VV—vertical transmit/vertical receive—and HH—horizontal transmit/horizontal receive) are generally less useful than cross-polarised (HV and VH) SAR data for AGB measurements; a cross-polarised sensor configuration is sensitive to the changes in polarisation produced by scattering elements within a tree canopy [76].
Several SAR satellites are currently operational. Each SAR satellite works within a specific radar frequency band (with a corresponding wavelength), with an X-, C-, S-, L- or P-band sensor listed in order of increasing wavelength. Longer wavelength SARs (i.e. L- and P- band) have a greater ability to penetrate the surface and canopy cover. The signal interacts with objects at the same scale or larger than its wavelength, with smaller objects not affecting the backscatter. As a result, longer wavelength SAR signals pass through leaves and small branches in the upper canopy and offer more information about differences in larger woody material such as stems and large branches [77] making them more suitable for AGB estimation as large branches and stems comprise the highest percentage of AGB in forests. However, smaller antenna size, higher spatial resolution and reduced power consumption have favoured the use of shorter wavelengths from space-borne SAR systems, which are sensitive to smaller canopy elements such as leaves and small branches.
The sensitivity of L-band SAR backscatter to AGB saturates at around 100–150 t ha−1 [78, 79]. However, some authors have found higher saturation values of more than 250 t ha−1 for L-band [80] and even more than 300 t ha−1 when combined with other SAR datasets such as X-band [81]. Nevertheless, there is no current satellite sensor in orbit (neither optical nor radar) that can offer a reasonable relationship between the observations and the high values of AGB often found in tropical areas (>400 t ha−1) [79, 80, 82,83,84,85]. A P-band SAR such as the planned BIOMASS mission is needed to retrieve very high AGB [86].
Current Methods to Map AGB
Most methods to map AGB can be included in two broad types based on the spatial scale of the approach: small to medium scale methods and large scale methods (Table 1). The first type (small-medium) covers from project size scale to countrywide scale. These approaches are not usually restricted by ground data or air- and space-borne image availability, except in some tropical countries. The second type (large scale) includes spatial scales beyond national borders such as continental or biome level (large countries will also be included here). Ground data availability is the main constraint for calibrating and validating these large scale approaches. At this level, the use of airborne data would be impractical and overly costly.
These projects are generally based on a combination of in situ data and satellite sensors with moderate to coarse spatial resolutions (25 m to ca. 55 km). A large amount of different remotely sensed datasets are available, ranging from passive optical, to LiDAR and SAR from either air- or space-borne platforms. All these approaches face the limitations of remote sensing imagery to map forest AGB (i.e. ground data paucity, signal saturation, cloud cover, topography). Most methods use a combination of multiple datasets in order to overcome these limitations. Data synergy approaches enable an exploitation of the specific strengths of each sensor. However, AGB data availability to calibrate these methods is still an important constraint, especially at scales beyond the national level.
Methods to map AGB over large spatial scales can also be separated into parametric and non-parametric approaches. Parametric approaches make assumptions on the shape of the distribution of the data, while non-parametric approaches make fewer or no assumptions. The use of parametric models present bigger challenges for upscaling or extrapolating AGB data, as there are no current satellite observations that can be reasonably related to AGB across the whole landscape. Additionally, the assumptions in parametric models of independence and multivariate-normality are often violated [87]. As complex ecological systems like forests show non-linear relationships, autocorrelation and variable interaction across temporal and spatial scales, non-parametric algorithms often outperform parametric ones [88]. Examples of parametric methods are multiple regression analysis (e.g. [13]) or geostatistical methods such as co-kriging (e.g. [89]), whereas the k-nearest neighbour technique (e.g. [90]), random forests [13, 21] and neural networks (e.g. [91]) are examples of non-parametric methods.
Small-Medium Mapping Scale
The methods used to map AGB from small to medium scale are generally calibrated with forest inventory plot data. However, there is an increasing tendency to use airborne LiDAR as calibration data [105, 106, 109,110,111]. This type of approach relates AGB field observations to airborne LiDAR data, and then calibrates the parameter retrieval from space-borne sensors using those LiDAR datasets. As mentioned before, the use of airborne data is only feasible at national level or below due to logistic and economic constrains.
A range of non-parametric machine-learning algorithms are used at national level to extrapolate AGB measured from forest plots [11, 21, 62, 63, 99, 102,103,104]. This approach can combine different types of data from high to coarse resolution. Passive optical imagery from high-resolution multispectral sensors such as RapidEye, AVNIR-2, SPOT-5, Pléiades and WorldView-2 are often used at this scale by means of supervised classifications, geostatistical approaches and texture analyses [50, 112, 113]. Moreover, forest AGB can also be estimated using canopy height models generated from stereo photogrammetric approaches [113,114,115,116]. Hyperspectral optical imagery from sensors such as Hyperion on board of the EO-1 satellite has shown to outperform multispectral optical imagery when mapping forest biomass and land cover classes [117]. Nevertheless, hyperspectral data show the best results when used in combination with other types of data such as SAR [47] or airborne LiDAR [118, 119]. Regression methods have also been applied at this level with moderate resolution imagery in Colombia [108] and Queensland (Australia) [80]. A previous study of AGB stocks at national level used 250 m spatial resolution imagery (MODIS, DEM and land cover layers) and forest inventory data to generate AGB maps for the USA by means of a classification and regression tree modelling [11]. Kellndorfer et al. [62] used a very similar approach over the USA but using 30 m resolution Landsat imagery from the National Land Cover Database, the US National Forest Inventory and SRTM topographic data.
At this scale, more complex techniques applied to SAR data can estimate other biophysical parameters such as tree canopy height, which can be used to estimate AGB indirectly from allometric models. This type of approach does not suffer from the AGB/signal saturation problem. Multiple SAR images of an area, if acquired from roughly the same position in space, and with the same image geometry such as look angle, polarisation, wavelength and spatial resolution, can be combined to take advantage of the phase information contained within each complex image, in a process called SAR interferometry (InSAR). Images can be acquired simultaneously by two receiving sensors in single-pass InSAR mode (e.g. the TanDEM-X satellite constellation), or at different times by the same or different sensors in repeat-pass InSAR mode (e.g. Sentinel-1A and 1B). While the distance between the sensors’ positions in space should be sufficiently large to provide sensitivity to signal phase differences, as this distance increases, there is spatial decorrelation of the signal, up to a point called the critical baseline, beyond which the phase of each image is completely decorrelated with respect to the other image [120]. From both techniques, it is possible to derive digital surface models (DSM) from the phase difference. This approach also requires an accurate digital terrain model (DTM) of the ground elevation beneath the canopy to estimate canopy height [68]. A dual wavelength approach could also be used to estimate a DTM of the ground, but the quality and the type of DTM will determine the accuracy of the AGB estimations (Fig. 1). The phase correlation between two acquisitions determines the reliability of InSAR measurements and is known as interferometric SAR coherence. For longer wavelengths, lower coherence between repeat-pass image pairs indicates the presence of denser vegetation, as scatter between image acquisitions increases with forest growing stock volume [121].
Vegetation carbon content at Monks Wood National Nature Reserve derived from the canopy height models from a LIDAR DSM and LIDAR DTM, b XVV InSAR DSM and LIDAR DTM, c XVV InSAR DSM and smoothed interpolated LHH InSAR DTM (dual wavelength approach). Warmer colours indicate higher carbon content (range from 5 to 400 t C ha−1). Adapted with permission from Balzter et al. [68]
Polarimetric interferometry (PolInSAR) is another SAR technique which, in contrast to single-polarisation InSAR, does not rely on an external DTM, as it estimates terrain and canopy height from the vertical heights of the scattering phase centres of the different polarimetric scattering mechanisms [122,123,124]. Different polarisations interact more strongly with different scatterers, such as canopy (HV) and trunk (HH). SAR tomography (TomoSAR) goes beyond the PolInSAR technique by using a set of multiple baselines of interferometric SAR images to generate a 3D vertical structure of the vegetation canopy based on the variation of backscattering as a function of height [86, 125]. Most of these techniques are difficult to use over large areas due to the restrictive data requirements. Better availability of SAR sensors allowing higher spatial and temporal resolution acquisitions might circumvent these limitations.
Large Mapping Scale
At large scales, data availability is the main limiting factor of AGB mapping approaches. Additionally, estimating AGB for very different ecosystems, such as tropical and boreal forest, using the same method can be very challenging due to the variations in forest structure, species composition, wood density, allometry, atmospheric effects and vegetation moisture.
Two recent map products [13, 15••] established a benchmark in the synergistic use of different earth observation datasets to map AGB across the whole tropical biome. These studies use AGB estimated from millions of GLAS footprints to calibrate their methods. The approach by Baccini et al. [13] relates GLAS waveforms to AGB using a model calibrated by ground plots directly located under the GLAS footprints, while Saatchi et al. [15••] use three plot-level continental allometric models derived from ground data to relate GLAS-derived Lorey’s height (H L) to AGB. The use of a model for each continent might better explain the allometric regional variability than a single model, but might still introduce a great amount of uncertainty when applied to different forest biomes. These studies used machine-learning algorithms such as random forest [87] and MaxEnt [126, 127] for upscaling of the AGB across wide areas, to produce 463 m and 1 km resolution maps, respectively. Saatchi et al. [15••] reported a relative error of approximately 30% across the three continents, while Baccini et al. [13] reported similar figures in terms of root mean square error (RMSE) (38–50 t ha−1). One of the most innovative features of the Saatchi et al. [15••] study was the possibility of mapping the uncertainty of the AGB estimation on a pixel-by-pixel basis. Both approaches use MODIS spectral bands and the SRTM digital elevation model as predictor variables, and in the case of Saatchi et al. [15••] also Quick Scatterometer data (QSCAT). These methods aim to take advantage of the full potential of the information contained in each input band, but none of these bands on its own can fully explain the variability of AGB across the landscape.
These two products provide very different results on the amount and spatial distribution of AGB at finer resolutions [128] (Table 2 and Fig. 1). Differences when compared to in situ AGB data or to local AGB maps have also been found [129, 130] but can be partially explained by the allometric models used to estimate AGB, different ground and remote sensing data, modelling techniques, pixel sizes and temporal coverage. Mitchard et al. [129] found that these maps do not agree with the spatial distribution of AGB in permanent Amazon field plots and that the uncertainties quantified in a comparison with 413 ground plots far exceed those reported by the studies. Saatchi et al. [131] responded to Mitchard et al. [129] arguing that, aside from methodological flaws in the interpolation approach, using 413 plots from different periods between 1956 and 2013 only represent 404.6 ha out of 650 million ha of forest in the Amazon and without a rigorously designed and extensive in situ forest inventory strategy are not representative of the AGB trends in the region. Nonetheless, the consistency of both products at coarser scales suggests that realistic estimates of carbon stocks can be produced over large regions.
The two pantropical carbon maps were fused using a methodology that incorporated research field observations, forest inventory plots and other high-resolution biomass maps [95•]. The method was based on bias-removal and weighted-averaging of the regional maps, and resulted in a pantropical map with a 15–21% lower RMSE than that of the input maps, and lower bias (mean bias 5 t ha−1 vs. 21 and 28 t ha−1 for the input maps).
Boreal and temperate forest GSV was mapped at 100 m and 1 km spatial resolution using hyper-temporal data series of Envisat ASAR ScanSAR backscatter imagery by means of a parametric semi-empirical model called BIOMASAR [17•]. The major advantage of this parametric semi-empirical approach is that the algorithm does not rely on training data. The high uncertainty of the 100 m resolution map (average 70% relative error) was considerably reduced (average 43%) when aggregating to coarser pixels of 1 km resolution. The applicability of this C-band SAR algorithm to tropical areas with much higher AGB density is unclear, but adapting the algorithm to use larger SAR wavelengths such as L-band could potentially overcome this problem. Thurner et al. [18] used the GSV estimated from this product in combination with specific wood density information and allometric relationships between biomass compartments (stem, branches, foliage and roots) to produce a C stock map for the boreal and temperate forests at ca. 1 km spatial resolution.
GSV at 500 m and AGB at 10 km were also mapped continentally for the whole of the European Union [98] using a downscaling approach that weighted the land cover class mean GSV values extracted from forest inventories by fractional cover maps developed using MODIS data. An Africa-wide map was also produced at 1 km resolution by extrapolating data from forest plots by means of MODIS imagery and a random forest algorithm, producing a RMSE of 50.5 t ha−1.
Early efforts to monitor forests at global level led to the Forest Resource Assessments (FRAs) by the United Nations (UN) Food and Agriculture Organization (FAO). These assessments are based on the analysis of forest inventory information supplied by each country and supported by expert judgements, remote sensing and statistical modelling [132, 133]. National Forest inventories are the most widely used method for in situ forest monitoring due to its historic roots in national forestry administrations, its accuracy and low technical requirements. The approach consists of sample-based statistical methods, sometimes in combination with remote sensing and aerial imagery. In developing countries where the labour cost is low, the use of forest inventories could be a relatively cost-effective approach. However, it was not until 2000 that a single technical definition for forest was used (>10% crown cover). Changes in baseline information, inconsistent methods and definitions through the different FRAs make their comparison difficult [134]. Several authors have questioned the country-level estimates of forest carbon stocks reported by the FRAs due to inadequate sampling for the national scale, inconsistent methods and in some tropical countries figures that were not based on actual measurements [4, 135, 136]. These assessments however do not generate spatial estimations of AGB, but national level statistics on forest cover, forest state (e.g. GSV), forest services and non-wood forest products.
First global AGB maps were not based on remote sensing imagery but on downscaling of FAO forest inventory statistics using annual net primary production NPP model outputs [93] and on the assignment of IPCC default AGB averages (estimated from FAO data) to GLC2000 [137] land cover classes [92]. Following the same fusion approach as Avitabile et al. [95•], a global map of AGB was generated for the GEOCARBON project [94], fusing the boreal map from Santoro et al. [96] and the pantropical map from Avitabile et al. [95•] at ca. 1 km pixel size. Hu et al. [97] recently published a global AGB map based on a combination of GLAS footprints, forest inventory data, optical imagery, climate data and land cover layers by means of a random forest approach. The AGB estimations of Hu et al. [97] seem to be much higher than previous global and pantropical maps (Fig. 2)
Vegetation optical depth (VOD) from Earth’s passive microwave radiation acquired by the Advanced Microwave Scanning Radiometer (AMSR-E) sensor was used to map AGB globally over a long time period (1993–2012) [72••]. The main disadvantage from this approach comes from the low energy of this radiation which only allows coarse resolutions (27.5 km pixel in this study). Additionally, there is no ground data available at these spatial scales that would allow calibration of such pixel sizes. In Liu et al.’s [72••] study, aggregated pixels from the Saatchi et al. [15••] map were used for calibration. As a result, any of the uncertainties from the Saatchi et al. [15••] map will propagate into this new product. Similar approaches are being investigated using ESA’s Soil Moisture and Ocean Salinity (SMOS) mission [73, 138].
Carbon trends estimated by Liu et al. [72••] are comparable in boreal and temperate areas to trends reported by Pan et al. [139••] calculated using ground observations for the period 2000–2007. However, both studies disagree in their estimations for tropical areas where the loss of AGB is much larger in the study of Liu et al. [72••] (Fig. 3). Pantropical carbon maps have divergent AGB estimations in comparison to ground data [129] being significantly larger in some regions [63]. This might explain the larger AGB loss found in tropical regions by Liu et al. [72••] in comparison to Pan et al. [139••], as the Saatchi et al. [15••] map was used as calibration of the approach.
Pantropical AGB maps [13, 15••] can differ in their estimations and might not agree with ground observations [63, 128,129,130]. Understanding the reasons behind these differences is crucial for improving contemporary retrieval methods. Initiatives such as the Biomass Geo-Wiki [140] use a crowdsourcing approach to compare and validate forest AGB products to address tasks related to gap analysis, cross-product validation, possible harmonisation and hybrid product development. The site allows the analysis of the pantropical carbon maps [13, 15••, 95•] and other continental and national level products. A similar initiative, based on the study by Mitchard et al. [128] which compared the tropical carbon maps [13, 15••] led to the development of the website “Comparing Global Carbon Maps” [141]. This site allows the interactive comparison between both maps, as well as between other carbon maps provided by different authors. The Global Forest Watch (GFW) platform has also been recently developed with the aim to improve forest information from remote sensing and ground observations [142]. The platform provides information on forest change, land cover (including AGB), land use, conservation and human interactions. The main dataset is the 12 years forest cover loss and gain product developed by Hansen et al. [53••] and a new AGB map at 30 m resolution based on the methodology used by Baccini et al. [13].
Future Scenario
At least three space-borne LiDAR sensors should be operational in the near future, inspired by the heritage of the ICESat satellite (GLAS sensor), which was widely used as a calibration/validation dataset for AGB mapping at biome and continental levels (Table 3). ICESat-2 will be launched in 2017 with the Advanced Topographic Laser Altimeter System (ATLAS) on board. The main objective of this satellite, as with the previous ICESat, is monitoring ice sheet elevation and sea ice thickness. The mission also has a secondary objective to estimate ground surface height, canopy height and canopy cover. However, it is not clear whether the ATLAS sensor will be suitable to estimate canopy height and AGB on forest areas due to concerns on the noise level of the discrete return photon-counting system [143, 144]. Additionally, AGB estimation by ATLAS in sparse forests such as the boreal taiga-tundras and savannas will be challenging due to the low sampling rate, the sole use of the green wavelength and the low sensitivity of the sensor to discern differences in AGB at 10 t ha−1 intervals [144, 145].
Two other LiDAR sensors specifically designed for forest structure characterisation will be attached to the International Space Station (ISS). The Global Ecosystem Dynamics Investigation LiDAR (GEDI) mission on board the ISS should be operational in 2018 [146]. The GEDI instrument will be composed of three laser transmitters that will acquire 14 parallel tracks of 25 m footprints [147]. The main objective of the GEDI mission is to quantify the spatial and temporal distribution of AGB carbon. The Multi-footprint Observation LiDAR and Imager (MOLI) should be operative in 2019 and will also be attached to the ISS [148]. This sensor will have two aligned nadir-viewing LiDARs to capture multi-footprints and a multiband imager (green, red and near-infrared) with 5 m resolution. The aim of this mission is to determine canopy height more precisely by the synergy between LiDAR and a high-resolution optical sensor able to provide information on crown size and approximate height. Unfortunately, GEDI and MOLI will not be able to obtain footprints from boreal forests (30% of world’s forest) due to the orbital characteristics of the ISS.
The forthcoming LiDAR sensors could be a game changer in the coming years, providing millions of LiDAR footprints to potentially characterise forest structure and AGB and could be used for calibration and validation of methods based on optical and SAR imagery. LiDAR profilers will certainly generate key datasets for mapping AGB at large scales and be a realistic solution for the AGB data availability problem. Approaches such as the ones presented by Saatchi et al. [15••] and Baccini et al. [13] will also be feasible to replicate. These approaches are based on non-parametric algorithmic methods (i.e. MaxEnt and Random Forest), which are often more suitable to model complex ecosystems such as forests [15••]. The drawback of these approaches is the lack of calibration/validation data in several parts of the world. Semi-empirical methods such as the BIOMASAR algorithm [17•], which do not require ground data for algorithm calibration, would be very promising if adapted to longer SAR wavelengths such as L-and P-band.
There is a wide range of optical multispectral sensors relevant for monitoring vegetation (e.g. Landsat 7 ETM+, Landsat 8 OLI, Sentinel-2A/3A, SPOT 6/7, MODIS and PROBA-V), as this has traditionally been the most widespread technology used by Earth Observation Satellites. In the period between 2017 and 2021, we will see a continuation of programmes such as Landsat and Sentinel with the new Landsat 9 and additional Sentinel satellites (2B, 2C, 3B and 3C) being launched (Table 3). All these new sensors ensure the continuity of the optical archive, which started with the Landsat programme more than 40 years ago, as well as the large scale and coarse spatial resolution sensors AVHRR, MERIS and MODIS. The Sentinel-2 satellites provide the highest resolution (10 m) operational free-of-charge optical imagery currently available, improving over the 30 m resolution imagery provided by Landsat satellites. Hyperspectral technology is still underrepresented on satellite platforms but planned satellites such as the EnMAP (2018) and PRISMA are very promising.
Governments and space agencies are currently starting to recognise the advantages of SAR sensors for a wide range of applications. There are more SAR instruments in space than ever before, and numbers are to increase steadily in the coming years (Table 3). Radar has several characteristics that are an advantage for forest monitoring, including cloud penetration (useful in very cloudy areas, such as over most tropical forests) and correlating strongly with AGB at long wavelengths such as L-band. Current short-wavelength X-band (2.4–3.8 cm) SAR satellites such as the TerraSAR-X and COSMO-SkyMed constellations will be complemented by the Paz Satellite (2017) and the second generation of COSMO-SkyMed (2018–2019). C-band SAR (3.8–7.5 cm) satellite programmes such as Radarsat and Sentinel-1A/1B will also continue with new additions in future years with the new Radarsat constellation (2018) and Sentinel 1C (2021). The only S-band satellite (Huanjing 1C) will have a continuation with NovaSAR-S (2017). Larger wavelengths such as L-band (15–30 cm) ALOS-2 will have continuation with the SAOCOM 1A (2017), 1B (2018) and SAOCOM Companion Satellite (CS) Mission (2018). SAOCOM 1A/1B will fly in constellation with COSMO-SkyMed forming the SIASGE L+X-band SAR System. SAOCOM-CS is a receive-only dual-pol sensor platform designed to fly in formation with SAOCOM-1A/1B. This orbital combination will allow techniques such as SAR polarimetry, polarimetric SAR interferometry and SAR tomography. The NASA-ISRO Synthetic Aperture Radar (NISAR) mission (2021) will be the first dual-frequency SAR satellite (L- and S- band).
A larger wavelength than L-band is however better suited to estimating high AGB levels, and the BIOMASS P-band (30–100 cm) sensor is therefore very promising [86]. The BIOMASS mission is due to be launched in 2021. This mission by the European Space Agency (ESA) has the following accuracy requirements at 200 m pixel level: a RMSE of ±10 t ha−1 for AGB below 50 t ha−1 and a relative error of ±20% for AGB above 50 t ha−1. If successful, this will be the first space-borne P-band SAR and will be sensitive to high AGB (Fig. 4). The mission however is restricted to measure outside of the US Space Objects Tracking Radar (SOTR) area [151]. This means that the sensor will have to be turned off over North America, Central America and Europe. Nevertheless, most AGB rich tropical forests worldwide will still be surveyed by the BIOMASS satellite.
P-band HV backscattering coefficient plotted against aboveground biomass for experiments conducted at six different forest sites. The green squares with error bars indicate the mean and standard deviation of the data points within intervals of ±10 t ha−1 centred on values of biomass spaced by 20 t ha−1, beginning from 50 t ha−1 and running out to 270 t ha−1. The solid green line is a regression curve derived from the combined data reported in the publications prior to 2009. The dashed curves are obtained by replacing the biomass value, B, by 0.8 × B and 1.2 × B in the regression equation. Reprinted with permission from Le Toan et al. [86]
Optical and SAR imagery sense the vegetation by means of different physical processes which have different sensitivity to AGB. SAR imagery has a higher AGB saturation point than optical imagery according to the literature [79, 80, 82,83,84,85], but recent studies have also found that optical infrared imagery might have correlation to AGB beyond its theoretical saturation point [13, 62]. As the theoretical saturation point of current SAR L-band imagery lies around 150 t ha−1 [78, 152], we will have to wait for the P-band BIOMASS mission to be able to estimate AGB in high biomass regions (over 200 t ha−1). However, none of these sensors can be used alone for AGB estimation globally, either because of limitations in signal saturation, coverage, cloud cover persistence or complex signal retrieval due to topography. The use of data synergy approaches makes it possible to exploit the specific strengths of each sensor. Aiming to better characterise and to reduce uncertainties of AGB estimates by identifying limitations of current datasets and methods to estimate AGB and by developing innovative synergistic mapping approaches; ESA established the Data User Element (DUE) GlobBiomass project [153]. The project works in five regions covering boreal, temperate and tropical forest biomes (Mexico, South Africa, Poland, Sweden and Kalimantan) developing map products for the years 2005, 2010 and 2015 [154] and a global map for the year 2010 [155]. The use of these approaches might allow the generation of an AGB baseline before the BIOMASS mission is in orbit.
Conclusion
This review has shown current methods to estimate AGB using passive and active space-borne remote sensing technology. Most approaches are limited by ground data availability for calibration/validation, signal saturation with AGB, coverage of the sensor, cloud cover persistence or complex signal retrieval due to topography. This highlights the importance of synergistic approaches which aim to overcome these limitations by exploiting the advantages of several sensors. Several promising techniques used at small scale (e.g. PolInSAR, TomoSAR) have not been tested yet at larger scales due to complexity and data requirements. However, this might change due to the imminent availability of high spatial and temporal resolution datasets being acquired by new sensors. The new generation of optical sensors (e.g. Sentinel-2), LiDAR profilers (ICESat-2, GEDI and MOLI) and SAR sensors (e.g. BIOMASS, SAOCOM and Sentinel-1) will allow the estimation of AGB to a spatial and temporal resolution never seen before and with an unprecedented accuracy.
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Acknowledgments
P. Rodriguez-Veiga and H. Balzter were supported by the UK’s National Centre for Earth Observation (NCEO). P. Rodriguez-Veiga was also supported by the ESA DUE GlobBiomass project - ITT AO/1-7822/14/I-NB and H. Balzter by the Royal Society Wolfson Research Merit Award, 2011/R3.
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Rodríguez-Veiga, P., Wheeler, J., Louis, V. et al. Quantifying Forest Biomass Carbon Stocks From Space. Curr Forestry Rep 3, 1–18 (2017). https://doi.org/10.1007/s40725-017-0052-5
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DOI: https://doi.org/10.1007/s40725-017-0052-5