Climate variability impacts CH4 wetland sources as changes in flux density per unit area and via expansion or contraction of wetland areas in response to surface hydrological processes. This paper is a first attempt to isolate the role of varying wetland area on the seasonal and interannual variability of CH4 wetland emissions over the past decade. Wetland area extent at monthly intervals was provided over the period 1993–2000 by a suite of satellite observations from multiple sensors. The regionally variable fraction of wetland area was optimized using satellite observations of flooded area as a first estimate and further adjusted to match the seasonal cycle of CH4 fluxes retrieved from a global atmospheric inversion. Wetland flux densities of CH4 were calculated by coupling the ORCHIDEE global vegetation model with a process-based wetland CH4 emission model, calibrated by optimizing its parameters at the site level against representative CH4 flux time series. For boreal bogs north of 50°N, we found that variations in area contributed about 30% to the annual flux. For temperate and tropical wetlands, the variations in area has almost no influence on the annual CH4 emissions but contributes significantly to the seasonal behavior, accounting for 40% and 66% of the seasonal amplitude of fluxes, respectively. In contrast, the interannual variability of wetland area appears to be the dominant cause of interannual variations in regional CH4 emissions from wetlands at all latitudes (largest in the tropics), with up to 90% of annual flux anomalies explained by wetland area anomalies in some years. For example, in 1998, boreal wetlands north of 50°N contributed to approximately 80% of the positive anomaly according to our calculations. We also found that climate anomalies can lead to both increased emitting areas and decreased flux densities at the same time, with opposite effects on the total CH4 flux entering the atmosphere. With a view to forecasting the future trajectory of atmospheric methane content, our results point to the absolute necessity to be able to predict the variations in wetland extent, a hydrological problem, in order to affirm the reliability of simulations of changing methane emissions perturbed by climate.
If you can't find a tool you're looking for, please click the link at the top of the page to "Go to old article view". Alternatively, view our Knowledge Base articles for additional help. Your feedback is important to us, so please let us know if you have comments or ideas for improvement.
 Atmospheric methane (CH4) plays a key role in climate both as a greenhouse gas and as a reduced compound controlling the global oxydizing capacity of the atmosphere [Houghton et al., 2001]. Its growth rate in the atmosphere decreased since the early 1990s, but shows considerable interannual variation [Dlugokencky et al., 2001; Bousquet et al., 2006]. Natural wetland emissions are the largest single source in the global CH4 budget and also the most uncertain, ranging from 115 [Fung et al., 1991] up to 237 TgCH4/yr [Hein et al., 1997], representing 20 to 40% of the global source. Wetland CH4 emissions seem to dominate the interannual variability of the global CH4 source [Walter et al., 2001b; Bousquet et al., 2006], and they are even suspected to be the main cause of the stalled CH4 growth rate since 1999 [Bousquet et al., 2006]. Wetland CH4 emissions arise from the combination of changes in the flux density and in the wetland area, both driven by changing weather and climate [Christensen et al., 2003]. For instance, temperature fluctuations will control the rates of methanogenesis and the length of the growing season in northern wetlands but also the area of wetlands through surface evaporation. Similarly, precipitation controls variations in CH4 flux density through changes in the water table depth, but also the regional wetland area. Finally, both temperature and rainfall determine Net Primary Productivity (NPP), which contributes to substrate availability for CH4 production under anaerobic conditions.
 In previous global modeling studies of CH4 emissions from wetlands, the variability of wetland area was calculated with simple assumptions. Walter et al. [2001b] assumed a fixed spatial distribution of wetlands [Matthews and Fung, 1987] and introduced seasonality by computing the water table depth using a 1-D hydrological model. Shindell et al.  diagnosed the wetland spatial distribution using thresholds for climate parameters. Kaplan  used an algorithm combining topography with calculated soil moisture. The goal of our study is to separate the contribution of area from that of flux density in the seasonal and interannual variability of CH4 emissions by wetlands over the past decade. To do so, we use two models: the ORCHIDEE global vegetation model [Krinner et al., 2005] and the process-oriented wetland emission model of Walter et al. [2001b]. We optimize some parameters using a dual constraint approach. The parameters controlling the flux density were optimized against site-level observations. The parameters controlling the seasonal cycle of wetland area in each region were optimized using a global remote sensing data set of flooded area [Prigent et al., 2001, 2007] and atmospheric inverted fluxes [Bousquet et al., 2006]. The optimized CH4 emission model was then integrated globally over the period 1993–2000 to separate the role of climate-induced varying area from varying flux density in the seasonal and interannual variability of wetland CH4 emissions over the globe.
2. Methodology and Experimental Design
2.1. Methane Production at the Site Level
 We used the process-based model developed by Walter et al. [2001a] and hereafter referred as W01. This model simulates methane flux densities from natural wetlands and calculates methanogenesis in the saturated deeper soil horizons, methanotrophic oxydation in the aerated upper soil, and upward transport by diffusion, ebullition and/or plant-mediated transport [Walter and Heimann, 2000]. In the original W01 formulation, the methane production rate Rprod, in each pixel for time t and depth z, is a function of NPP and temperature given by
 The base rate of methanogenesis R0 (μmol L−1 h−1) provides the amount of substrate available for methanogenesis. f(NPP) (dimensionless) is a function describing the seasonal fluctuations of the available substrate as well as its vertical distribution; this function is based on the seasonal cycle of NPP, and f(T) (dimensionless) is a step function equal to 0 if T(t, z) < 0°C and equal to 1 in all other cases; if the soil temperature drops below 0°C in one of the soil layers, there can be no methane production from this specific layer. This function only controls the ability of a specific soil layer to produce or not CH4. The Q10 parameter then defines the temperature dependency of methane production. The strategy of W01 was to calibrate the value of R0 using data from six field sites, regressing R0 versus soil temperature and NPP. There is, however, no direct process-related relationship between NPP and R0 [Christensen et al., 2003; Conrad, 1989; Whiting and Chanton, 1993] except, perhaps for the exudation of sugars by roots which should be in lockstep with NPP [Hütsch et al., 2002]. Regardless, some previous studies have shown that the contribution of recent photosynthates to emissions is relatively low [i.e., King and Reeburgh, 2002].
 We modified the global calculation of Rprod according to equation (2) and replaced R0 by a linear function of the labile soil carbon pool, CL, as suggested by Cao et al.  and Khvorostyanov et al. . Daily values of CL (expressed in μmol dm−2), and some other inputs necessary for W01, are computed at each grid point by the ORCHIDEE global vegetation model [Krinner et al., 2005] run here in a non-water-stress configuration (see section 2.2). The base rate of methanogenesis (α0, in dm−1 h−1) is a parameter that we have optimized. In equation (2), we have kept the function that vertically distributes the carbon in the soil, forg(z), which was part of f(NPP) in equation (1), because this distribution cannot be computed by ORCHIDEE.
 We have also optimized the Q10 value, a parameter which was initially set to 6 at all sites and even globally by W01, although its reported values in the literature range from 1.6 to 16 [Valentine et al., 1994]. This large reported range encompasses the temperature response of at least two processes: the substrate production and methanogenesis itself. Studies which measured Q10 for methanogenesis only report values in the range 1.2 to 3.5 [Conrad, 1989; Kelly and Chynoweth, 1981]. Thus the temperature dependency for methanogenesis derived from CL is expected to be different than the one regressed from NPP by W01. We decided not to optimize the metanotrophy-related parameters and hence to restrict our calibration only to the flooded phase of the wetlands, i.e., when the water table depth reaches soil surface and methanotrophy can be neglected (see details in sections 2.2 and 2.3).
2.2. Simulations Carried Out With the ORCHIDEE Global Vegetation Model
 We calculated the CH4 flux density over each wetland grid point on the basis of our updated version of the model developed by W01. Key input data are the water table depth, the soil temperature profile, and the labile soil carbon. For the water table depth, we made the assumption that it remains close to soil surface all year-round. This is the main hypothesis of our work: CH4 emissions by wetlands are dominated by the time periods during which the water table depth is at the surface. This assumption results from the use in the following (section 3.1) of remote sensing data which only detects water-logged areas [Prigent et al., 2001, 2007]. Soil temperature and carbon were computed by the global vegetation model ORCHIDEE [Krinner et al., 2005]. In ORCHIDEE, the soil temperature profile is calculated with a seven layers scheme and soil carbon depends on plant functional type and climate. We ran a global 1° × 1° simulation assuming no water stress at any grid point in order to better represent the wetlands soil carbon (via better representation of NPP) and soil temperature computation: soil water content was prescribed at its maximum value throughout the entire length of the simulation. ORCHIDEE was forced with the present-day vegetation map of Loveland et al. , the soil color map of Zobler  for soil albedo, and the hourly climate forcing data of Ngo-Duc et al. . A spin-up run of several thousands of years was run to bring all carbon pools to their long-term equilibrium values. The 1993–2000 interannual simulation was then carried out. Since there is no specific plant functional type (PFT) for wetlands in ORCHIDEE, any flooded PFT (boreal, temperate and tropical forest or grassland) is assumed to be a potential wetland. Crops areas, however, are excluded in our calculations of CH4 emission and so are rice paddies (not represented in ORCHIDEE). Oxygen limitations on plant growth are not accounted and the simulated wetland NPP is likely to be high-biased. Other inputs of the Walter's model are root depth, soil depth, and the efficiency of plant-mediated transport. These data were derived by matching the 11 plant functional types of ORCHIDEE with the biome-specific values given by W01.
2.3. Site-Level Model Optimization
 The α0 and Q10 parameters have been optimized against local time series of CH4 flux measurements at three different sites listed in Table 1 in a strategy similar to that of Petrescu et al. . These sites are a bog site in northern Finland (the Abisko site, M. Jackowicz-Korczynski, unpublished data, 2006), a peatland site in Michigan [Shannon and White, 1994], and a swamp site in Panama [Keller, 1990]. They represent the three main categories of wetland areas as defined by Fung et al.  and Cao et al.  as the boreal bogs (>50°N), the temperate bogs (20°N–50°N), and the tropical swamps (30°S–20°N), respectively.
Table 1. Sites Selected for the Optimization of the Two Parameters Chosena
Chosen (α0, Q10) Pair
α0 (10−6 m−1 month−1)
RMSE (mg m−2 month−1)
Production rate, α0. Temperature dependency of methanogenesis, Q10.
 We first sampled the output from the global simulation of ORCHIDEE (described above) at the location of each calibration site. CH4 emissions were then calculated and parameters α0 and Q10 were adjusted in order to minimize the root mean square error (RMSE) between observed and modeled monthly emissions. Optimization was only carried out at time periods during which the water table depth was at the surface or above to be consistent with our main hypothesis (section 2.2). We assume, too, that there is no longer delay than a few days between potential emissions and the beginning of inundation. Figure 1 provides, for Abisko, a map of the RMSE in the α0 and Q10 plane. This map, or cost function to be minimized, shows that the (α0, Q10) couple corresponding to absolute minimum of RMSE (as reported in Table 1) is located in a flat “valley” of (α0, Q10) couples that all share a RMSE close to the minimum (10% above absolute minimum area is shaded in the Figure 1). In order to derive an uncertainty range on α0 and Q10 parameters value that will be propagated into regional CH4 flux calculations, we also tested four other couples (α0, Q10) within the low-RMSE valley. These couples have the highest α0, the highest Q10, the lowest α0, or lowest Q10 values, respectively, within the RMSE ≤ 1.1 * RMSEmin valley. These different pairs are reported in Table 1, are represented by triangles in Figure 1, and will be used in the following to estimate error ranges for the simulated fluxes.
 At both the Abisko and Michigan sites, the Q10 value is close to 3, i.e., half the value chosen by W01, but close to the maximum value measured for methanogenesis [Conrad, 1989; Kelly and Chynoweth, 1981]. At the tropical (Panama) site, the optimized Q10 is found to be only of 1.48 ± 0.56, and this low value is rather well constrained by the flux data. It is also imposed by the lowest bound of the range given by Conrad . This low Q10 value results from the anticorrelation between temperature and flux density at this specific site: when temperature increases, flux density decreases and vice versa. Because we are looking at only one site that may not be representative of the whole tropics, and since having a higher Q10 in the tropics could change the relative importance of the flooding mechanism in terms of its contribution to variability of CH4 emission, we have chosen another (α0, Q10) pair to be tested, with a Q10 value that is closer to the boreal one and the associated α0 that minimizes RMSE (Table 1).
 Contrary to Q10, the optimized value of α0 is larger for the tropical site than for the other sites (by a factor of ∼5). This order of magnitude between the tropical site and the others concerning the amount and the quality of substrate is consistent with what Walter and Heimann  also discussed for R0. The larger discrepancy between sites at different latitudes may also result from the very weak number of carbon soils pools in ORCHIDEE (e.g., not accounting for the exudates pool) and the simple way in which carbon dynamics is computed.
Figure 2 (left) (Figures 2a, 2c, and 2e) compares the seasonal cycle of simulated and observed CH4 emissions at each site, with their respective error bars when available. At the Abisko site, the amplitude of the seasonal cycle of the CH4 flux, as well as the length of the emission season, are well captured by the optimized model. However, the peak of CH4 emissions is about 1 month early compared to the site observations. The ORCHIDEE model lacks a parameterization of frozen soils, which qualitatively explains this earlier maximum. At the temperate (Michigan) site, the modeled flux agrees quite remarkably with the observed one.
 At the tropical (Panama) site, the optimized model shows no seasonal cycle of CH4 flux over the 7 month flooded period of selected observations, although the data suggest higher emissions from October to November (∼20 gCH4/m2/month) than from May to August (∼12 gCH4 m−2 month−1). Errors associated to the observed fluxes are too large to provide a tight constraint of the model parameters. At this site, ORCHIDEE simulates no seasonal variations of NPP, nor of the labile carbon and of soil temperature, which is the reason why the modeled CH4 flux remains constant all year-round at this site.
3. Methane Emission Upscaling to the Global Level
3.1. Satellite Observed Wetland Area Distribution
 We integrated our optimized emission model over the globe, forced with outputs from our 1° × 1° ORCHIDEE run. The seasonal and interannual variability of wetland extent comes from the remote sensing product developed by Prigent et al. [2001, 2007] at a horizontal resolution of 0.25° by 0.25°. This data set provides us with the fractional inundated area per pixel and per month, and covers the 1993–2000 time period. It therefore quantifies the existence of stagnant water throughout the globe, but not of methane production (that we compute according to equation (2)). It is the only data set (to our knowledge) providing global and temporal information on the variability of natural wetland areas. It is constructed using a combination of satellite data including passive microwave observations and a linear mixture model to account for vegetation [Prigent et al., 2001, 2007]. For the boreal regions, as the microwave measurements are sensitive to the snow cover, snow masks were used to edit the results and avoid any confusion with snow covered pixels. The weekly North Hemisphere and South Hemisphere snow mask from the National Snow and Ice Data Center (NSIDC) is adopted and averaged on a monthly basis [Armstrong and Brodzik, 2005].
 We have filtered the Prigent et al. [2001, 2007] data set interpolated at 1° resolution in order to exclude lakes (IGBP land cover data set [Loveland et al., 2000]). In lakes, most of the CH4 produced in the sediment is oxydized before reaching the surface [Walter and Heimann, 2000], except maybe for Arctic thermokarst lakes that are subject to warming in winter [Zimov et al., 1997; Walter et al., 2006] and for some tropical dams established over flooded forests [Abril et al., 2005]. We have also excluded all rice paddy areas [Matthews et al., 1991]. The resulting global map of wetland extent is shown in Figure 3, together with its interannual variability, the mean annual number of inundated months, and the timing of maximum flooding. More detailed information concerning the seasonal and interannual behavior of specific regions can be found in the work of Papa et al.  and Papa et al. [2007, 2008a] for the Indian subcontinent and the boreal regions, respectively.
3.2. Optimization Approach
 Flooded areas from Prigent et al. , once filtered for lakes and rice paddies, were further adjusted to only retain those inundated pixels that are CH4 emitters. Flooded river valleys, for example, or inundated nonorganic soils will not emit CH4. This implies the active wetland area to be smaller than the satellite-observed area. At the face value, the multisatellite approach has difficulty to detecting small, isolated water patches in areas with a large dry fraction. This may imply the active wetland area to be higher than satellite observed. We thus have more confidence on the variability, on seasonal and year-to-year scales, of flooded area than on the mean average value. Accordingly, we tuned the flooded area by a regionally uniform multiplier βarea that is calculated in order to minimize the RMSE between our bottom-up model fluxes and the top-down monthly fluxes aggregated into large latitudinal bands (boreal, temperate, and tropical; see below) from the Bousquet et al.  atmospheric inversion (hereafter referred to as B06).
 The B06 inverse modeling quantitatively links atmospheric CH4 measurements and regional sources and sinks. For the period 1984–2003, the CH4 concentration responses to the action of OH sinks and regional surface sources were simulated for each month with the three-dimensional chemistry transport model LMDZ-INCA [Hauglustaine et al., 2004]. The model was forced with interannual analyzed winds [Uppala et al., 2005] and interannually varying OH concentrations as constrained by methyl-chloroform observations [Bousquet et al., 2005]. Emissions of CH4 from different regions of the globe by distinct processes, together with the photochemical sinks, were inferred and their uncertainties reduced by matching atmospheric observations within their uncertainties in a Bayesian formalism [Bousquet et al., 2005]. Long-term measurements of the 13C/12C ratio in CH4 (δ13C-CH4) were also used as an additional constraint on the partitioning of microbial-, biomass-burning-, and fossil-fuel-related CH4 sources. Prior sources were from inventories [Fung et al., 1991; Van der Werf et al., 2003, 2004; Olivier and Berdowski, 2001]. Note that no interannual variability was assigned to the prior sources, so interannual variations of atmospheric concentrations were built through the inversion procedure. B06 performed a control inversion, which is used in this work, supplemented by an ensemble of 17 sensitivity inversions (varying a priori error of regional fluxes, etc.). B06 shows a very good fit to observations both for interannual and seasonal variations, demonstrating that the seasonality of inverted emissions is consistent with atmospheric measurements of methane.
 The optimization of βarea was carried out for three major latitudinal zones. Each one consists of the grouped continental regions that were used in the TRANSCOM3 model intercomparison experiment [Gurney et al., 2002]. This choice is made to be consistent with the top-down approach results (B06) used. The boreal band includes Boreal North America, Europe, and Boreal Eurasian TRANSCOM regions. The temperate band includes temperate North America, northern Africa, and temperate Eurasia. The tropical band includes South America, southern Africa, tropical Asia, and Australia. Each of the three zones has a separate and unique set of methane flux parameters (α and Q10) that is derived from the optimizations carried out at the site level located within each band (see section 2.3). This breakdown into three categories sharing the same parameters is obviously idealized compared to reality where wetlands cover a large diversity of ecosystems with distinct Redox, pH, or nutrient status [Mitsch and Gosselink, 2000]. However, given the lack of site-level data, it would have been unreasonable to try to include more details.
 For each major group of regions and each of the five (α0, Q10) pairs selected (six in the tropics) in our sensitivity tests (section 2.3), we have optimized βarea for each individual year (1993 to 2000). The CH4 fluxes presented hereafter were calculated, for each (α0,Q10) pair, using three different values of βarea: the mean over the 8 years and the mean ± 1 standard deviation. The optimized values of βarea are 0.68 ± 0.08, 1.19 ± 0.17, and 1.04 ± 0.12 for the boreal (>50°N), the temperate (20°N–50°N), and the tropical (30°S–20°N) latitudinal belts, respectively. The sixth tropical pair of (α0, Q10) chosen, with increased Q10 value, does not change the βarea value. In the temperate belt, βarea is larger than one, suggesting that emitting areas should be increased compared to the prior satellite value. This may reflect wet areas that have not been detected by the satellite product, or wet areas where the water table depth lies just below the soil surface.
 The monthly emission of methane per pixel, fCH4(x, t), in g CH4/month, is finally calculated according to
where S(x, t) and FCH4(x, t) are the fraction of the pixel x that is inundated during month t and the flux density for pixel x and month t, respectively. FCH4(x, t) is taken from the output of W01 after modification of methanogenesis production rates following equation (2) and optimization of α0 and Q10. The resulting space and time varying maps of wetland CH4 fluxes are thus compatible with the measured CH4 fluxes at the three calibration sites, the satellite observed patterns of flooded surfaces, and the latitudinally averaged B06 inversion fluxes. Figure 2 (right) (Figures 2b, 2d, and 2f) shows the seasonal and interannual variability of wetland emissions for each latitudinal band. The agreement between fCH4(x, t) and the inversions of B06 is very good at boreal and temperate latitudes, although the minimum value of the top-down CH4 flux in winter is always larger than the one we simulate. In the tropical belt, however, there is no agreement between the top-down and bottom-up estimates, even after adjustment of βarea. Not only is the amplitude of the seasonality of our simulated fCH4(x, t) much smaller than the one estimated by B06 (∼50%), but the timing of maximum emissions is shifted.
 If we focus, for instance, on the tropical South American TRANSCOM region, variations of CH4 emissions from B06 follow precipitation (the correlation (r2) equals to 0.38 over 1993–2000). This could be partly explained by nudging of the inversion results to their a priori flux temporality. The a priori flux of B06 comes from a combination of the Fung et al.  flux density and the Matthews and Fung  static data for wetland surface extent. CH4 emissions are maximum in the work of Fung et al.  when monthly precipitation exceeds monthly potential evaporation. The inversion has changed the magnitude, but not the timing of the emissions. Oppositely, in the P07 area data set which underpins our bottom-up modeling, precipitation often precedes inundation by a few months. For example, over the tropical South American TRANSCOM region, we have calculated that the best correlation (r2 = 0.6) between rainfall and P07 wetland extent is obtained with a lag of 3 months. In these tropical regions, inundation, through the floodplain mechanisms, is likely due to precipitation events upstream. For a region as tropical South America, this may explain the shift of emissions between B06 and our approach. Discrepancy between B06 and our results at larger space scales (30°S–20°N belt) could be also explained by the fact that the northern and southern hemisphere contributions to the flux are weighted differently in the different estimates of wetland area used [Matthews and Fung, 1987; Prigent et al., 2007]. Despite these differences, the total annual emissions coming from the tropics is of the same order of magnitude in both B06 and our approach.
4. How Much Do the Fluctuations in Wetland Area Contribute to the Seasonal and Interannual Variability of CH4 Fluxes?
 We have carried out three sensitivity simulations to assess the contribution of seasonal and interannual variations of wetland extent to the total CH4 wetland flux to the atmosphere. The first simulation, called VAR, is forced by the variable wetland extent of Prigent et al. [2001, 2007] over 1993–2000. The second simulation, called FIXED, is forced monthly by a fixed climatological wetland area (mean annual area or mean area over the emitting season). The third simulation called CLIM is forced by a climatological (averaged over the 8 years of satellite observations), seasonally variable, wetland area. The range of sensitivity tests with varied parameters (sections 2.3 and 3.2) are used to derive errors bars in those calculations. The percent change of total annual CH4 emissions (per latitude band per year) is used to evaluate the contribution of wetland extent variations at both time scales: seasonal and interannual.
4.1. Annual Mean and Seasonal Variability (VAR Versus FIXED Simulations)
 The mean seasonal cycle of wetland CH4 emissions, averaged over the period 1993–2000, is illustrated in Figure 4. A mean annual flux of 40.8 Tg CH4 yr−1 is emitted by bogs in the boreal belt, of which 33.7% (±2.9%) is attributed to the seasonal increase in flooded area, with larger emitting surfaces in July and August and almost no active surfaces from November to April. If we had prescribed, as W01 did previously, the maximum extent of wetland area to run our FIXED run instead of the mean value over the flooded season, we would have simulated a larger mean annual boreal CH4 flux, but the variability explained by changes in area would still have been larger than 30%. If we use another metric for this evaluation: the variation of amplitude of the mean seasonal cycle (rather than the total annual flux) to measure the contribution of changing area to CH4 emissions, we obtain a decrease of 45.7% (±0.6%) in amplitude from VAR to FIXED. In all cases, the contribution of wetland extent to methane emissions (annual values and seasonal cycle) is significant and range between 30 and 50%.
 A flux of 51.0 Tg CH4 yr−1 is emitted by wetlands in the temperate belt, but the contribution of area extent changes to the mean annual flux is close to 0%. This results from reduced amplitude of the seasonal cycle of flooded areas and the longer emitting season in temperate regions that leads to increased winter values and decreased summer ones. For both temperate and boreal wetlands, the flux density is positively correlated with the extent: when the extent is maximum during summer, the density is also maximum mainly driven by temperature. This is why the VAR and FIXED fluxes are perfectly in phase (Figure 4). However, in the temperate belt, flux densities are not zero during winter unlike boreal regions. Thus, removing wetland seasonality (from VAR to FIXED simulations) results in an increase in wetland area during winter and a decrease during summer that compensate each other. This leads, however, to a decrease in mean seasonal cycle amplitude of 40.0% (±1.0%).
 For tropical wetlands where we simulate the largest annual CH4 flux (∼102 Tg CH4 yr−1), the situation is quite similar: seasonal variations of the extent do not significantly contribute to the mean annual flux (∼1.4% ± 1.0). Accounting explicitly for variable area (VAR compared to FIXED) introduces a seasonality in the fluxes, with larger (smaller, respectively) fluxes during the February–August (September–January, respectively) period of the year, resulting in small changes of the annual mean but leads to a decrease of 66.4% (±1.4%) for seasonal amplitude. The seasonality of tropical CH4 fluxes is hence dominated by the seasonality of wetland area (Figure 4), regardless of the value of Q10: if it is low as derived from the optimization procedure or it is as large as that of the boreal regions.
4.2. Interannual Variability (VAR Versus CLIM Simulations)
 We now analyze the effect of interannually variable versus interannually fixed but seasonally variable wetland area. The CLIM flux anomalies are plotted versus the VAR ones in Figure 5 for each latitudinal band. In the three latitudinal bands, no simple relationship with good statistical significance (measured using a r2 regression coefficient) that correlates the CLIM and the VAR anomalies was found. This indicates that interannual changes in wetland CH4 emissions result from a nontrivial combination between climate induced changes in flux densities and changes in wetland areas, with a little covariance between these two factors.
 The points that lie near the origin of the CLIM-VAR scatterplot exhibit a small interannuality and will therefore not be further discussed (e.g., years 1993, 1994, 1996, and 1997 in the boreal regions). The points that lie between the x axis and the 1:1 line mark the years when the anomaly in CH4 flux is amplified by the anomaly in wetland area. The climate anomaly that drives an increase (resp. a decrease) in CH4 flux is at the same time driving a larger (a smaller, respectively) extent of emitting areas. Examples of this positive covariance between area and flux density are 1998 and 2000 in the boreal belt, during which 79.1 ± 26.2% and 88.3 ± 0.6%, respectively, of the total methane flux anomaly is explained by anomalies in wetland areas when compared to the climatology, the rest being caused by anomalous flux density. In the temperate belt, close to or more than 50% of the CH4 anomaly is explained by changes in area for years 1995 (90.7 ± 2.0%), 1996 (73.7 ± 3.6%), and 1999 (49.9 ± 1.1%). In the tropics, changes in area explain most of the interannual variability in wetland CH4 fluxes emissions, most of the points being next to the x axis. Even with increased Q10, our conclusion is not altered (gray markers in Figure 5). Moreover, quantification of the contribution of wetland extent to interannual variability of CH4 emissions is independent of the chosen β.
 There are some years, however, in the boreal and temperate zones when climate anomalies drive increases (decreases, respectively) in CH4 flux per unit area, while they drive a decrease (increase, respectively) in wetland extent. Accounting for such a negative covariance therefore dampens or even compensates for the effects of changing flux density. In 1998, for example, in the temperate belt, climate forcing alone led to negative flux density anomalies, while the resulting flux shows a positive anomaly when variable area is considered. In 1999, in the boreal belt, the flux anomaly has a lower magnitude when the variability of area is included. The CLIM anomalies are quite similar between years 1996 and 2000 in the tropical zone (small anomalies), while the VAR anomalies between these 2 years are opposite in sign and quite large. All these examples suggest that climate variability can affect areas and flux densities in different and complex ways. The climate dependency of processes controlling inundated area (rainfall and potential evaporation) and CH4 flux density (labile carbon production and temperature) are indeed different. This finding is parallel to the observation that there is no simple relationship between wetland area and rainfall or temperature [Prigent et al., 2007], suggesting that nonclimatic factors, or other variables controlling the surface water budget may also play an important role in the establishment and resilience of wetlands (destruction of peat soils by fires like in Indonesia in 1997 [Page et al., 2002] or in the Moscow region in 2002). Flooding can occur in response to locally intense precipitation. However, they can also be driven by snowmelt or heavy precipitation at upstream locations [Prigent et al., 2007; Papa et al., 2007]. In these cases, inundation and precipitation are separated in both time and space. For instance, relations between precipitation, wetlands extent, and water storage (using GRACE satellite) were explored by Papa et al. [2008b].
 If we specifically focus on the year 1998, Dlugokencky et al.  attributed the high positive flux anomaly in atmospheric CH4 content to wetlands located north of 30°N (∼11.6 Tg CH4 yr−1) and in the tropics (∼13 Tg CH4 yr−1), while our calculations are quite different from those (5.4 T Tg CH4 yr−1 and −0.8 Tg CH4 yr−1, respectively). If we assume their anomalies were most probably overestimated by up to 40% as the authors themselves seem to suggest, we end up with quite similar anomalies for northern wetlands but quite different and even oppositely sign values for the tropics. For wetlands located north of 30°N, change in wetland extent explains almost all of the positive anomaly during the considered year (from VAR to CLIM the anomaly becomes close to zero or negative according to the parameters' value). Our negative anomaly in tropical regions results both from the changes in wetland extent (decrease) and in flux density (decrease). In our simulation, it is a negative anomaly in the active carbon stock that drives the simulated fluxes. This negative anomaly results from increased heterotrophic respiration (caused by increased surface temperature) that overcompensates the increased growth primary productivity and leads to decreased carbon accumulation. This negative anomaly is obtained even with a large Q10. In the original version of Walter et al.'s [2001a] model and in its adaptation used by Dlugokencky et al. , the amount of substrate (R0) is mainly dependent on temperature, and thus, flux densities always increase when temperature increases.
 We have developed a global process-based CH4 emission model forced globally by input from the ORCHIDEE global vegetation model and driven by varying climate. The modeled fluxes are calibrated at local scale against flux measurements from three sites, and at the scale of large latitude bands using remote sensing data on seasonally flooded areas. We showed that over the time period 1993–2000, variability in wetland area strongly influences in the seasonal and interannual variability of CH4 emissions. At the seasonal time scale, variable flooded area mainly plays a role in controlling variable fluxes at boreal latitudes (∼30%). In the temperate regions and in the tropics, variations in area do not influence the annual emissions (∼0% in the temperate zone and less than 2% in the tropics) but explain a large part of the seasonality amplitude. At the interannual time scale, however, variable area is the main source of interannual variability in the global CH4 wetland source at all latitudes, especially in the tropics. Because regional patterns of climate variability can affect in opposite (and nontrivial) ways the wetland area and the CH4 flux density, it is absolutely necessary to compute the changes in extent to correctly predict the current and future behavior of CH4 emissions in response to climate.
 We have, however, neglected variations of the water table depth, an important factor controlling CH4 fluxes [Liblik and Moore, 1997; Shurpali and Verma, 1998] in nonsaturated wetlands. Indeed, the wetland extent data set that we used does not sense those areas. Not accounting for this factor could (1) amplify the importance played by wetland areas fluctuations in our results and (2) explain some disagreement between our approach and top-down results in tropics where changes in the water table seem to dominate seasonal cycle of wetland CH4 emissions [Walter et al., 2001a]. Moreover, P07 inundation fractions can include areas where the water table is well above the soil surface such that oxidation can occur in a standing water column [Walter and Heimann, 2000]. In a following work, we can match information given by P07 and information about the value of water table depth given by satellite altimeters on continental water bodies. An improvement in W01 would also be necessary to account for the oxidation in a water column.
 Our approach could also be refined, since labile carbon has been computed by ORCHIDEE assuming soils to be water saturated all year long, while in reality, the plant production and soil carbon decomposition rates during the flooded and nonflooded period may be different. Moreover, we need to better account for the limitation of carbon decomposition under anoxic conditions in ORCHIDEE.
 This research was supported by the project Impact-Boreal, funded by the Agence Nationale pour la Recherche (ANR). We also thank M. Jackowicz-Korczynski and T.Christensen for the Abisko data. Computing support was provided by Commissariat à l'Energie Atomique (CEA).