Dealing with spatial heterogeneity in pointwise-to-gridded- data comparisons
- 1Atomic and Molecular Physics (AMP) Division, Harvard–Smithsonian Center for Astrophysics, Cambridge, MA, USA
- 2Department of Civil, Structural and Environmental Engineering, University at Buffalo, Buffalo, NY, USA
- 3Research and Education in Energy, Environment and Water Institute, University at Buffalo, Buffalo, NY, USA
- 4Earth Science Division, NASA Ames Research Center, Moffett Field, CA, USA
Correspondence: Amir H. Souri (firstname.lastname@example.org)
Most studies on validation of satellite trace gas retrievals or atmospheric chemical transport models assume that pointwise measurements, which roughly represent the element of space, should compare well with satellite (model) pixels (grid box). This assumption implies that the field of interest must possess a high degree of spatial homogeneity within the pixels (grid box), which may not hold true for species with short atmospheric lifetimes or in the proximity of plumes. Results of this assumption often lead to a perception of a nonphysical discrepancy between data, resulting from different spatial scales, potentially making the comparisons prone to overinterpretation. Semivariogram is a mathematical expression of spatial variability in discrete data. Modeling the semivariogram behavior permits carrying out spatial optimal linear prediction of a random process field using kriging. Kriging can extract the spatial information (variance) pertaining to a specific scale, which in turn translates pointwise data to a gridded space with quantified uncertainty such that a grid-to-grid comparison can be made. Here, using both theoretical and real-world experiments, we demonstrate that this classical geostatistical approach can be well adapted to solving problems in evaluating model-predicted or satellite-derived atmospheric trace gases. This study suggests that satellite validation procedures using the present method must take kriging variance and satellite spatial response functions into account. We present the comparison of Ozone Monitoring Instrument (OMI) tropospheric NO2 columns against 11 Pandora spectrometer instrument (PSI) systems during the DISCOVER-AQ campaign over Houston. The least-squares fit to the paired data shows a low slope ( molecules cm−2, r2=0.66), which is indicative of varying biases in OMI. This perceived slope, induced by the problem of spatial scale, disappears in the comparison of the convolved kriged PSI and OMI ( molecules cm−2, r2=0.72), illustrating that OMI possibly has a constant systematic bias over the area. To avoid gross errors in comparisons made between gridded data vs. pointwise measurements, we argue that the concept of semivariogram (or spatial autocorrelation) should be taken into consideration, particularly if the field exhibits a strong degree of spatial heterogeneity at the scale of satellite and/or model footprints.
Most of the literature on validation of satellite trace gas retrievals or atmospheric chemical transport models assumes that geophysical quantities within a satellite pixel or a model grid box are spatially homogeneous. Nevertheless, it has long been recognized that this assumption can often be violated; spatially coarse atmospheric models or satellites are often not able to represent features, nor physical processes, transpiring at fine spatial scales. Janjić et al. (2016) used the term representation error to describe this complication. They posit that this problem is a result of two combined factors: unresolved spatial scales and physiochemical processes. To elaborate on this definition, let us assume that an atmospheric model simulating CO2 concentrations can represent the exact physiochemical processes but is fed with a constant CO2 emission rate. This model obviously cannot resolve the spatial distribution of CO2 concentration because we use an unresolved emission input. As another example, if we know the exact rates of CO2 emissions but use a model unable to resolve atmospheric dynamics, the spatial distribution of CO2 concentrations will be unrealistic due to unresolved physical processes.
Numerous scientific studies have reported on this matter. The simulations of short-lifetime atmospheric compounds such as nitrogen dioxide (NO2), isoprene, formaldehyde (HCHO), and the hydroxyl radical (OH) have been found to be strongly sensitive to the model spatial resolution (Vinken et al., 2011; Valin et al., 2011; Yu et al., 2016; Pan et al., 2017a). Likewise, the performance of weather forecast models in resolving non-hydrostatic components heavily relies on both model resolution and parameterizations used. For example, when Kendon et al. (2014), Souri et al. (2020a), and Wang et al. (2017) defined a higher spatial resolution in conjunction with more elaborate model physics, they were able to more realistically simulate extreme or local weather phenomena such as convection and sea–land breeze circulation.
The spatial representation issue is not only limited to models. Satellite trace gas retrievals optimize the concentration of trace gases and/or atmospheric states to best match the observed radiance using an optimizer along with an atmospheric radiative transfer model. This procedure requires various inputs such as surface albedo, cloud and aerosol optical properties, and trace gas profiles, all of which come with different scales and representation errors. Moreover, the radiative transfer model by itself has different layers of complexity with regards to physics. A myriad of studies have reported that satellite-derived retrievals underrepresent spatial variability whenever the prognostic inputs used in the retrieval are spatially unresolved (e.g., Russell et al., 2011; Laughner et al., 2018; Souri et al., 2016; Goldberg et al., 2019; Zhao et al., 2020). Additionally, the large footprint of some sensors relative to the scale of spatial variability of species inevitably leads to some degree of the representativity issues (e.g., Souri et al., 2020b, Tang et al., 2021; Judd et al., 2020). It is because of this reason that several validation studies resorted to downscaling their relatively coarse satellite observations using high-resolution chemical transport models so that they could compare them to spatially finer datasets such as in situ measurements (Kim et al., 2018; Choi et al., 2020). Nonetheless, their results largely arise from modeling experiments which might be biased.
The validation of satellites or atmospheric models is widely done against pointwise measurements. Mathematically, a point is an element of space. Hence, it is not meaningful to associate a point with a spatial scale. If one compares a grid box to a point sample (i.e., apples to oranges), they are assuming that the point is the representative of the grid box. At this point, the fundamental question is the following: can the average of the spatial distribution of the underlying compound be represented by a single value measured at a subgrid location? This question was answered in Matheron (1963). He advocated the notion of the semivariogram, a mathematical description of the spatial variability, which finally led to the invention of kriging, the best unbiased linear estimator of a random field. A kriging model can estimate a geophysical quantity in a common grid. This is not exclusively special; a simple interpolation method such as the nearest neighbor has the same purpose. The power of kriging lies in the fact that it takes the data-driven spatial variability information into account and informs an error associated with the interpolated map. This strength not only makes kriging a relatively superior model over simplified interpolation methods, but also reflects the level of confidence pertaining to spatial heterogeneity dictated by both data and the semivariogram model used through its variance (Chilès and Delfiner, 2009).
Different studies leveraged this classical geostatistical method to map the concentrations of different atmospheric compounds at very high spatial resolutions (Tadić et al., 2017; Li et al., 2019; Zhan et al., 2018; Wu et al., 2018). To the best of our knowledge, Swall and Foley (2009) is the only study that used kriging for a chemical transport model validation with respect to surface ozone. They suggested that kriging estimation should be executed in grids rather than discrete points. Kriging uses a semivariogram model in a continuous form. Optimizing the kriging grid size (i.e., domain discretization) at which the estimation is performed is an essence to fully obtaining the maximum spatial information from data. Another important caveat with Swall and Foley (2009) is that averaging discrete estimates (points) to build grids is not applicable for remote sensing data. Depending on the optics and the geometry, the spatial response function can transform from an ideal box (simple average) to a sophisticated shape such as a super Gaussian function (weighted average) (Sun et al., 2018). Moreover, the footprint of satellites is not spatially constant. We will address these complications in this study using both theoretical and real-world experiments.
Our paper is organized with the following sections. Section 2 is a thorough review of the concept of the semivariogram and kriging. We then provide different theoretical cases, their uncertainty, sensitivities with respect to difference tessellation, grid size, and the number of samples. Section 3 proposes a framework for satellite (model) validation using sparse point measurements and elaborates on the representation error using idealized experiments. Section 4 introduces several real-world experiments.
The semivariogram is a mathematical representation of the degree of spatial variability (or similarity) in a function describing a regionalized geophysical quantity (f), which is defined as (Matheron, 1963)
where x is a location in the geometric fields of V, f(x) is the value of a quantity at the location of x, and h is the vector of distance. If discrete samples are available rather than the continuous field, the general formula can be simplified to the experimental semivariogram defined as
where Z(xi) (and Z(xj)) is discrete observations (or samples), N(h) is the number of paired observations separated by the vector of h. The operator indicates the length of a vector. The condition of is to allow certain tolerance for differences in the length of the vector. For simplicity, we only focus on an isotropic case, meaning we rule out the directional (or angular) dependency in γ(h). Under this condition, the vector of h becomes scalar ().
If a reasonable number of samples is present, one can describe γ(h) through a regression model (e.g., Gaussian or spherical shapes). The degree of freedom (dof) for this regression is
where p is the number of parameters defined in the model. For instance, to fit a Gaussian function to the semivariogram with three parameters (p=3), three paired (N=3) observations are required at minimum. Different regression models can be used to describe γ(h) depending on the characteristic of the quantity of interest. In this study, we will use a stable Gaussian function:
where a and b are fitting parameters. A non-linear least-squares algorithm based on the Levenberg–Marquardt method will be used to estimate the fitting parameters.
The kriging estimator predicts a value of interest over a defined domain using a semivariogram model derived from samples (Chilès and Delfiner, 2009). The kriging model is defined as (Matheron, 1963)
where Y(x) is a zero-mean random function, and m(x) is a systematic drift. If we assume m(x)=a0, the model is called ordinary kriging. Similar to an interpolation problem, the estimation point is determined by linearly combining n number of samples with their weights (λj):
where is the estimation, λ0 is a constant weight, xj is the location of samples, and Z(xj) is point data (i.e., samples). The mean squared error of this estimation can be written as
where Z0 is point observations (Z0=Z(xj), ), and a0 is the mean of Z which is unknown. In order to estimate the weights, we are required to minimize Eq. (7), but this cannot be done without knowing the exact value of a0. A solution is to assume λ0=0 and impose the following condition:
This condition warrants be zero and removes the need for the knowledge of a0. Therefore Eq. (7) can be written as
where γj1j2 is the spatial covariance between the point observations and γj10 is the spatial covariance of between the observations and the estimation point. The spatial covariance is modeled by a semivariogram. Using the method of Lagrange multiplier and considering the constraint on the weights, Eq. (9) can be minimized by solving the following problem (Chilès and Delfiner, 2009):
where μ is the Lagrange parameter and x0 is the location of estimation. The first term in the right-hand side of this equation shows the spatial variability described by the semivariogram model among samples, whereas the second term indicates the modeled variability between samples and the estimation point. The unknowns (the left-hand side of the equation) have a unique solution if, and only if, the semivariogram model is positive definite and the samples are unique (Chilès and Delfiner, 2009). The estimation error can be obtained by
This equation is an important component in the kriging estimator. Not only can we estimate Z(x) given a selection of data points, but also an uncertainty associated with such estimation can be provided.
2.2 Theoretical cases
2.2.1 Sensitivity to spatial variability of the field
The present section illustrates the application of ordinary kriging for several numerical cases. Five idealized cases are simulated in a grid of 100×100 pixels, namely, a constant field (C1), a ramp starting from zero in the lower left to higher values in the upper right (C2), an intersection with concentrated values in four corridors (C3), a Gaussian plume placed in the center (C4), and multiple Gaussian plumes spread over the entire domain (C5). We randomly sample 200 data points from each field as is and successively create the semivariograms in 100 binned distances. Except C1, which lacks a spatial variability and thus γ(h)=0, other semivariograms are fit with the stable Gaussian function. Using the semivariogram model, we solve Eq. (10) to estimate for each pixel (i.e., 100×100) with the estimation errors based on Eq. (11). Figure 1 depicts the truth field (Z(x)), semivariograms made from the samples, estimated values (, difference of Z(x) and , and error associated with the estimation.
As for C1, the uniformity results in a constant semivariogram leading the estimation to be identical to the truth. This estimation signifies the unbiased characteristic of ordinary kriging. C1 is never met in reality; however, it is possible to assume some degree of uniformity among data restrained to background values; a typical example of this can be seen in the spatial distribution of a number of trace gases in pristine environments such as NO2 (e.g., Wang et al., 2020) and HCHO (Wolfe et al., 2019). Under this condition, any data point within the field (i.e., the satellite footprint) can be assumed to be representative of the spatial variability in truth.
Concerning C2, the semivariogram shows a linear shape, meaning data points at larger distances exhibit larger differences. Generally geophysical samples are uncorrelated at large distances; thereby one expects the semivariogram to increase more slowly as the distance increases. The steady increase in γ(h) is indicative of a systematic drift in the data invalidating the assumption of m(x)=a0. In many applications, a simple polynomial can explain m(x) and subsequently be subtracted from the data points. An example of this problem is tackled by Onn and Zebker (2006); it concerns the spatial variability of water vapor columns measured by GPS signals. Onn and Zebker (2006) observed a strong relationship between the water vapor columns and GPS altitudes resulting from the vertical distribution of water vapor in the atmosphere. Because of this complication, a physical drift model describing the vertical dependency was fit and removed from the measurements so that they could focus on the horizontal fluctuations. In terms of C2, one can effortlessly reproduce Z(x) by fitting a three-dimensional plane to barely three samples, indicating that the semivariogram is of little use.
C3 is an example of an extremely inhomogeneous field manifested in the stabilized semivariogram at a value of γ∼500, called the sill (Chilès and Delfiner, 2009), indicating insignificant information (variance) from the samples beyond this distance (∼20), called the range. Range is defined as the separation distance at which the total variance in data is extracted. The smaller the range is, the more heterogeneous the samples will be. While the estimated field roughly captures the shape of the intersections, it is spatially distorted at places with relatively sparse data points. The kriging model error is essentially a measure of the density of information. It converges to zero in the sample location and diverges to large values in gaps.
C4 is a close example of a point source emitter with faint winds and turbulence. The semivariogram exhibits a bell shape. As samples get further from the source, the variance diverges, stabilizes, and then sharply decreases. This is essentially because many data points with low values, apart from each other, have negligible differences. This tendency is recognized as the hole effect, which is characterized for high values to be systemically surrounded by low values (and vice versa). It is possible to mask this effect by fitting a semivariogram model stabilizing at a certain sill (like the one in Fig. 1). Nonetheless, if the semivariogram shows periodic holes, the fitted model should be modified to a periodic cosine model (Pyrcz and Deutsch, 2003).
The last case, C5, shows a less severe case of the hole effect previously observed in C4. This is due to the presence of more structured patterns in different parts of the domain. The range is roughly twice as large as the previous case (C4), denoting that there is more information (variance) among the samples at larger distances. A number of experiments using this particular case will be discussed in the following subsections.
2.2.2 Sensitivity to the number of samples
It is often essential to optimize the number of samples used for kriging. The kriging estimator somewhat recognizes its own capability at capturing the spatial variability through Eq. (11). Thus, if the target is spatially too complex and/or the samples are too limited, the estimator essentially informs that is unreliable through large variance. However, there is a caveat; Y(x) must be a Gaussian random model with a zero mean so that kriging can capture the statistical distribution of given the data points. Except this case, the kriging variance can either be underestimated or overestimated depending on the level of skewness of the statistical distribution of Y(x) (Armstrong, 1994). Figure 2 shows the kriging estimation for C5 using 5, 25, 50, 100, and 500 random samples in the entire field. Immediately apparent is a better description of the semivariogram when a larger number of samples is used, which in turn results in a better estimation of Z(x). The optimum number of samples to reproduce Z(x) depends on the requirement for the relative error ( being met at a given location.
2.2.3 Sensitivity to the tessellation of samples
A common application of kriging is to optimize the tessellation of data points for a fixed number of samples to achieve a desired precision. In real-world practices, the objective of such optimization is very purpose-specific; for example, one might prefer a spatial model representing a certain plume in the entire domain. Different ways for data selection exist (e.g., Rennen, 2008), but for simplicity, we focus on four categories: purely random, stratified random, a uniform grid, and an optimized tessellation. Figure 3 demonstrates the estimation of C5 using 25 samples chosen based on those four procedures.
Concerning the random selection, the lack of samples over two minor plumes causes the estimation to deviate largely from the truth. While a random selection may seem to be practical because it is independent of the underlying spatial variability, it can suffer from undersampling issues, thus being inefficient. As a remedy, it might be advantageous to group the domain into similar zones and randomly sample from each, which is commonly known as stratified random selection. We classify the domain into four zones by running the k-mean algorithm on the magnitudes of Z(x) (not shown) and randomly sample six to seven points from each one (total 25). We achieve a better agreement between the estimated field and the truth because we exploited some prior knowledge (here the contrast between low and high values).
As for the uniform grid, we notice that there are fewer data points in the semivariogram stemming from redundant distances, which is indicative of correlated information. Nonetheless, if the desired tessellation is neutral with regard to location, meaning that all parts of the domain are of equal scientific interest, the uniform grid is the most optimal design for the prediction of Z(x) under an ideally isotropic case. A mathematical proof for this claim can be found in Chilès and Delfiner (2009).
To execute the last experiment, we select 25 random samples for 1000 times and find the optimal estimation by finding the minimum sum of . It is worth mentioning that the optimized tessellation is essentially a local minimum based on 1000 kriging attempts. The optimized location of samples seems to be more clustered over areas with large spatial gradients. Not too surprisingly, we observe the smallest discrepancy between the estimation and the truth.
A lingering concern over the application of these numerical experiments is that the truth is assumed to be known. The truth is never known; this means we may never exactly know how well or poorly the kriging estimator is performing. However, it is highly unlikely for some prior understandings or expectations of the truth to be absent. If this is the case, which is rare, a uniform grid should be intuitively preferred to deliver the local estimations of average values in uniform blocks. In contrast, if the prior knowledge is articulated by previous site visits, model predictions, theoretical experiments, pseudo observations, or other relevant data, the tessellation needs to be optimized.
It is important to recognize that the uncertainties associated with the prior knowledge directly affect the level of confidence in the final answer. Accordingly, the prior knowledge error should ultimately be propagated to the kriging variance. The determination of the prior error is often done pragmatically. For example, if the goal is to design the location of thermometer sites to capture surface temperature during heat waves using a yearly averaged map of surface temperature, it would be wise to specify a large error with this specific prior information to play down the proposed design. This is primarily because the averaged map underrepresents such an atypical case. A possible extension of this example would be to use a weather forecast model with quantified errors capable of capturing retrospective heat waves. Although a reasonable forecast in the past does not necessarily guarantee a reasonable one in the future, it is rational to assume for the uncertainty with a new tessellation design using the weather model forecast to be lower than that using the averaged map.
A general roadmap for the data tessellation design is shown in Fig. 4. As proven in Chilès and Delfiner (2009), if the field is purely isotropic, the uniform grid is the most intuitive sensible choice when the prior information on the spatial variability is lacking. When the prior knowledge with quantified errors is available, an optimum tessellation can be achieved by running a large number of kriging models with suitable γ(h) and picking the one yielding the minimum difference between the prior knowledge and the estimation. The choice of the cost function (here L1 norm) is purpose-specific. For example, if the reconstruction of a major plume was the goal, using a weighted cost function, geared towards capturing the shape of plume, would be more appropriate.
2.2.4 Sensitivity to the grid size
A kriging model can estimate a geophysical quantity at a desired location considering the data-driven spatial variability information. Since the kriging model is practically in a continuous form, the desired locations can be anywhere within the field of V. A question is whether or not it is necessary to map the data onto a very fine grid. There is a trade-off between the computational cost and the accuracy of the interpolated map. The range of the underlying semivariogram helps in finding the optimal solution. The greater the range is (i.e., a more homogeneous field), the less important to map the data in a finer grid are.
Figure 5a depicts an experiment comparing the estimates of C2 at different grid sizes with the truth. The departure of the estimate from the truth is rather negligible for several coarse grids (e.g., 10×10). The homogeneous field, manifested by the large range (Fig. 1), allows for a reasonable estimation of Z(x) at coarse resolutions with inexpensive computational costs. Figure 5b shows the same experiment but on C5 with the optimized tessellation. As opposed to the previous experiment, the estimate substantially diverges from the truth when increasing the grid size, suggesting that a finer resolution should be used for fields with smaller ranges (i.e., heterogeneous fields).
The complexity of directly using the range for choosing the optimal grid size arises from the fact that the level of spatial homogeneity can vary within the domain. In fact, the range is derived from a semivariogram model representing a crude estimate of varying ranges occurring at various scales. It is intuitively clear that depending on the degree of heterogeneity, which is spatiotemporally variable, the grid size needs to be adaptively adjusted (Bryan, 1999). For the sake of simplicity, but at a higher computational cost, we adopt a numerical solution which is to first simulate on a coarse grid and then on a finer one until the difference with respect to the previous grid size across all pixels reaches an acceptable value (<1 %). We name this output (1×1) with the optimized tessellation for C5 as C5opt.
3.1 Synching the scales between the gridded field and satellite pixels
To minimize the complications of different spatial scales between two gridded data, we first need to upscale the finer-resolution data to match the coarse ones. In case of numerical chemical transport or weather forecast models, the size of the grid box is definitive. Likewise, a satellite footprint, mainly dictated by the sensor design, the geometry, and signal-to-noise requirements (Platt et al., 2021), is known. However, the grid size of the kriging estimation is a variable subject to optimization which has been discussed previously. When we compare the grid size of the kriging estimate to that of a satellite (or a model), three situations arise: first, the kriging spatial resolution is coarser than the satellite, a condition occurring when either the field is homogeneous or the field is undersampled. In situations where the field is homogeneous (γ(h)≅0), it is safe to directly compare the data points to the satellite measurements without having to use kriging. If the undersampling is the case (see Fig. 2 with 5 samples), it is sensible to first investigate if the field is homogeneous within the satellite footprint using different data (if any). If the homogeneity is met, we can compare two datasets either without kriging or, to match the size of kriging grid cell, with the satellite footprint and statistically involve the kriging variance in the comparison (discussed later); nonetheless, the kriging estimate beyond the location of samples must be used with extra caution because their variance very quickly departs from zero to extremely large numbers (see Fig. 1). Thus, there is a compromise between increasing the number of paired samples between two datasets and enhancing the level of confidence in statistics. If independent observations suggest that there might be large heterogeneity within a satellite footprint, it is strongly advised against quantitatively comparing the points to the satellite observations. Second, the number of samples is fewer than three observations in the field, so it is in principle impossible to build a semivariogram. Validating a satellite under this condition is prone to misinterpretation because the spatial heterogeneity cannot be modeled. Nonetheless, if one presumes a good degree of homogeneity within the sensor footprint (such as very high-resolution remote sensing airborne data), the direct comparison of point measurements might be possible. Third, the satellite footprint is coarser than the kriging estimate. Under this condition, we upscale the kriging map to match the spatial resolution of the satellite using
where S is the spatial response function, is the coarse kriging field, is the convolution operator, y is shift, and is the fine field. In discrete form we can rewrite Eq. (12) in
where m and n are the dimension of the response function. The mathematical formulation of S[m,n] for a number of satellites can be represented by two-dimensional super Gaussian functions as discussed in Sun et al. (2018). Atmospheric models have a uniform response to the simulated values within a grid box; therefore, , where J is the matrix of ones. In the same way, the kriging variance should be convolved through
where a superscript of 2 denotes squaring, and and are the kriging variance matrices in the coarse and the fine grids, respectively.
To demonstrate the upscaling procedure, we use C5opt (1×1) and upscale it at six grid sizes (m,m) of 5×5, 10×10, 15×15, 20×20, 25×25, and 30×30. For simplicity, we consider ; this spatial response function results in averaging the values in the grid boxes. Figure 6 shows the resultant map overplotted with the samples along with the error estimation. Two tendencies from this experiment can be identified: first, the discrepancy of the point data and is becoming more noticeable as the grid size grows; this directly speaks to the notion of the spatial representativeness; large grid boxes are less representative of subgrid values. Second, the gradients of the field along with the estimation error become smoother primarily due to convolving the field with the spatial response function, which acts as a low pass filter.
We further directly compare to the samples (i.e., observations) shown in Fig. 7. We see an excellent comparison between at 1×1 resolution with the observations underscoring the unbiasedness characteristic of the kriging estimator. Conversely, the upscaled field gradually diverges from the observations. This divergence is the problem of scale.
3.2 Point to pixel vs. pixel to pixel
To elaborate on the problem of scale, we design an idealized experiment theoretically validating pseudo satellite observations against some pseudo point measurements. The pseudo satellite observations are created by upscaling the C5 truth (Z) to 30×30 grid footprint considering , meaning that the satellite is observing the truth but in a different scale (Fig. S1 in the Supplement). The pseudo point measurements are the ones used for C5opt. Figure 8a shows the direct comparison of the satellite pixel with the point observations. By ignoring the fundamental fact that these two datasets are inherently different in nature, displaying the same geophysical quantity at different scales, we observe a perceived discrepancy (r2=0.64). The comparison suggests a wrong conclusion that the satellite observations are biased low. This discrepancy is unrelated to any observational or physical errors, rendering any physical interpretation of the comparison biased due to spatial-scale differences in the datasets. Figure 8b depicts the comparison of each grid box of the upscaled kriging estimate (30×30) with that of the satellite. This direct comparison shows a strong degree of agreement (r2=0.98), shaking off the erroneous idea of directly comparing point data to gridded data when the field exhibits substantial spatial heterogeneity.
Yet, the comparison misses an important point: the kriging estimate is considered error-free. We attempt to incorporate the kriging variance through a Monte Carlo linear regression method. Here, the goal is to find an optimal linear fit such that is minimized. and are the variances of y (here the satellite) and x (the kriging variance), respectively. We set the errors of y to zero and randomly perturb the errors of x based on a normal distribution with zero mean and a standard deviation equal to that of kriging estimate 15 000 times. The average of optimized a and b coefficients derived from each fit is then estimated, and their deviation at the 95 % confidence interval assuming a Gaussian distribution is determined. Figure 8b and c show the linear fit with and without considering the kriging error estimate. The linear fit without involving the kriging error gives a strong impression that it is nearly perfect, following closely to the paired observations. This is essentially explainable by the primary goal of χ2, which is to minimize the L2 norm of residuals , portraying a very optimistic picture of the satellite validation. The linear fit considering the kriging errors is different. The uncertainties associated with a and b are larger since x is variable (shown in horizontal error bars). The optimal fit gravitates towards the points with smaller standard deviations as they impose a larger weight. The confidence in the linear fit at higher values is lower due to their errors being large. This fit is a more realistic portrayal of the satellite validation.
Figure 9 summarizes the general roadmap for satellite (and model) validations against point measurements. To fit the semivariogram with at least two parameters, we are required to have three samples at minimum. Therefore, it is implausible to derive the spatial information from the point data where sampling is extremely sparse (<3 samples within the field). The only case of directly comparing point and satellite pixels is when the field within satellite footprint or the field in general is rather homogeneous, which is confirmed by independent data/models. Having more samples allows us to acquire some information on the spatial heterogeneity. The information carried by the data is considered more and more robust when increasing the number of samples. Subsequently, the kriging map along with its variance derived from a reasonable semivariogram at an optimized grid resolution should be convolved with the satellite response function so that we can conduct an apples-to-apples comparison. A real-world example on the satellite validation will be shown later.
4.1 Spatial distribution of NO2
We begin with focusing on tropospheric NO2 columns observed by the TROPOMI sensor (Copernicus Sentinel data processed by ESA and Koninklijk Nederlands Meteorologisch Instituut, KNMI, 2019; Boersma et al., 2018) at ∼ 13:30 LST. We choose NO2 primarily due to its spatial heterogeneity (e.g., Souri et al., 2018; Nowlan et al., 2016, 2018; Valin et al., 2011; Judd et al., 2020). We oversample good-quality pixels (qa_flag >0.75) through a physical-based gridding approach (Sun et al., 2018) over Texas at 3×3 km2 resolution in four seasons in 2019. We extract samples by uniformly selecting the NO2 columns in the center of each 30×30 km2 block. The semivariogram along with its model is calculated, and then we krige the samples. Figure 10 shows the NO2 columns map for four different seasons, the semivariogram, the kriging estimates, and the differences between the estimate and the field. High levels of NO2 are confined to cities, indicating that the sources are predominantly anthropogenic. Wintertime NO2 columns are larger than summertime mainly due to meteorological conditions and the OH cycle, the major sink of NO2. All semivariograms exhibit the hole effect. This is because of high values of NO2 being systematically surrounded by low values. Regardless of the season, we fit the stable Gaussian to variances at distances smaller than 2.5∘ (∼275 km2). The b parameter in Eq. (4) explaining the length scale is found to be 0.94, 0.88, 0.71, and 0.83∘ for DJF, MAM, JJA, and SON, respectively. These numbers strongly coincide with the seasonal lifetime of NO2 (Shah et al., 2020); wintertime NO2 columns are spatially more uniform around the sources; thus, in relative sense, they are more homogeneous (spatially correlated) than those in warmer seasons. On the other hand, the shorter NOx lifetime in summer results in a steeper gradient of NO2 concentrations. This tendency should not be generalized because transport and various NOx sources including biomass burning, soil emissions, and lightning can have large spatiotemporal variability resulting in different length scales at different times of a year. The differences between the kriging estimate and the field show some spatial structures indicating that NO2 is greatly heterogenous.
4.2 Optimized tessellation over Houston
The preceding TROPOMI data enabled us to optimize a tessellation of ground-based point spectrometers over Houston. Our goal here is to propose an optimized network for winter 2021 given our knowledge on the spatial distribution of NO2 columns in winter 2019 measured by TROPOMI. The assumption of using a retrospective NO2 field for informing a hypothetical future campaign is not entirely unrealistic. If we have a consistent number of pixels from TROPOMI between two years, it is unlikely for the spatial variance of NO2 to be substantially different for the same season. We follow the framework proposed in Sect. 2.2.3 involving randomly selecting samples from the field (for 50 000 iteration) and calculating kriging estimates for a given number of spectrometers. We then choose the optimum tessellation based on the minimum sum of .
Figure 11 shows the optimized tessellation given 5, 10, 15, and 20 spectrometers over Houston. The Houston plume is better represented with more samples being used. All cases share the same feature; the optimized samples are clustered in the proximity or within the plume. This tendency is clearly intuitive. We are required to place the spectrometers in locations where a substantial gradient (variance) in the field is expected. The difference between the kriging estimate and the TROPOMI observations using 20 samples does not substantially differ in comparison to the one using 15 samples. Therefore, to keep the cost low, a preferable strategy is to keep the number of spectrometers as low as possible while achieving a reasonable accuracy. Based on the presented results, the optimized tessellation using 15 samples is preferred among others because it achieves roughly the same accuracy as the one with 20 samples.
4.3 Validating OMI tropospheric NO2 columns during the DISCOVER-AQ 2013 campaign using Pandora
In order to understand ozone pollution (e.g., Mazzuca et al., 2016; Pan et al., 2017b, 2015), characterize anthropogenic emissions (Souri et al., 2016, 2018), and validate satellite data (Choi et al., 2020), an intensive air quality campaign was carried out in September 2013 over Houston (DISCOVER-AQ). The campaign encompassed a large suite of Pandora spectrometer instrument (PSI) (11 stations) measuring total NO2 columns with a high precision (2.7×1014 molecules cm−2) and a moderate nominal accuracy (2.7×1015 molecules cm−2) under the clear-sky condition (Herman et al., 2009). We remove the observations with an error of >0.05 DU, contaminated by clouds, and averaged them over the month of September at 13:30 LST (±30 min). We attempt to validate OMI tropospheric NO2 columns version 3.0 (Bucsela et al., 2013) refined in Souri et al. (2016) with the 4 km model profiles. The OMI sensor resolution varies from 13×34 km2 at nadir to km2 at the edge of the scan line. Biased pixels were removed based on cloud fraction >0.2, terrain reflectivity >0.3, and main (xtrack) quality flags =0. Following Sun et al. (2018), we oversample high-quality pixels in the month of September 2013 over Houston at 0.2×0.2∘ resolution. To remove the stratospheric contributions from PSI measurements, we subtract OMI stratospheric NO2 ( molecules cm−2) from the total columns over the area. Figure 12 shows the monthly-averaged tropospheric NO2 columns measured by OMI overplotted by 11 PSIs. The elevated NO2 levels (up to molecules cm−2) are seen over the center of Houston.
We then follow the validation framework shown in Figure 9 in which the number of point measurements and the level of heterogeneity are the main factors in deciding if we should directly compare them to the satellite pixels. Figure 13 shows the monthly-averaged PSI measurements along with the semivariogram and resulting kriging estimate at an optimized resolution ( data over the entire region) and errors. The distribution of the semivariogram suggests that there is a strong degree of spatial heterogeneity, necessitating the use of kriging. We fit a stable Gaussian to the semivariogram, resulting in . The spatial information (variance) levels off at 0.19∘ (∼21 km), with a maximum variance equal to 2.23 molecules2 cm−4. The measurements beyond this range (21 km) have a minimal weight due to this length scale. It is because of this reason that we see the kriging estimate converges to a fixed value at places being further than this range. The kriging errors of those grid boxes are constantly large (40 % relative error). The optimum grid size for kriging is found to be 2 km2 (<1 % difference across all grid boxes). Subsequently, we use the super Gaussian spatial response function described in Sun et al. (2018) to convolve both the kriging estimate and error within (see Fig. S2). Figure 14 shows the differences between the kriging estimate and error before and after convolution. The response function (OMI pixel) tends to be on average coarser than 2 km2, resulting in smoothing of both the kriging estimate and error.
We ultimately conduct two different sets of comparison: directly comparing PSI to OMI pixels and comparing convolved kriged PSI to OMI. It is worth noting that PSI measurements are monthly-averaged; similarly, OMI data are oversampled on a monthly basis. In terms of the PSI, we only account for grid boxes whose kriging error is below 1.2×1015 molecules cm−2 (1193 samples, 8 % of total kriging grid boxes). As for the grid-to-grid comparison, the kriging variance is considered in the linear polynomial fitted to the data through the Monte Carlo of the chi-square with 5000 iterations. The variability with the OMI stratospheric NO2 columns (0.16×1015 molecules cm−2) is added to the PSI error for both analyses. The left and right panels of Fig. 15 show the comparisons. As for the direct comparison of actual points (PSI) to pixels (OMI), the PSI measurements indicate a deviation of the slope (r2=0.66) from the unity line. This suggests that there is an unresolved magnitude-dependent systematic error. The grid-to-grid comparison not only offers a clearer picture of the distribution of data points, but also it hints at the offset being rather constant ( molecules cm−2; r2=0.72). We also observe that the statistics between the satellite and the benchmark are moderately improved. This comparison in general provides an important implication: the varying offsets in a plume shape environment (high to low values) are not necessarily due to variable offsets in the satellite retrieval, as the kriging estimate suggests that those varying offsets in point-to-pixel comparison, manifested in slope =0.76, are a result of varying spatial scales.
There needs to be increased attention to the spatial representativity in the validation of satellite (model) against pointwise measurements. A point is the element of space, whereas satellite (model) pixels (grid box) are (at best) the product of the integration of infinitesimal points and a normalized spatial response function. If the spatial response function is assumed to be an ideal box, the resulting grid box will represent the average. Essentially, no justifiable theory exists to accept that the averaged value of a population should absolutely match with a sample, unless all samples are identical (i.e., a spatially homogeneous field). This glaring fact is often overlooked in the atmospheric science community. At a conceptual level, we are required to translate pointwise data to the grid format (i.e., rasterization). This can be done by modeling the spatial autocorrelation (or semivariogram) extracted from the spatial variance (information) among measured sample points. Assuming that the underlying field is a random function with an unknown mean, the best linear unbiased predictions of the field can be achieved by kriging using the modeled semivariograms.
In this study, we discussed methods for the kriging estimation of several idealized cases. Several key tendencies were observed through this experiment: first, the range corresponded to the degree of spatial heterogeneity; a larger range indicated the lower presence of heterogeneity. Second, the kriging variance explaining the density of information quickly diverged from zero to large values when the field exhibited large spatial heterogeneity. This tendency mandates increasing the number of samples (observations) for those cases. Third, while the semivariogram models were constructed from discrete pair of samples, they are mathematically in a continuous form. It is because of this reason that we determined the optimal spatial resolution of the kriging estimate by incrementally making the grids finer and finer until a desired precision (=1 %) was met.
The present study applied kriging to achieve an optimum tessellation given a certain number of samples such that the difference between our prior knowledge of the field, articulated by previous observations, models, or theory, and the estimation is minimal. Usually there is uncertainty about the prior knowledge that should be propagated to the final estimates. The optimum tessellation for a range of idealized and real-world data consistently voted for placing more samples in areas where the gradients in the measurements were significant such as those close to point emitters.
This study also revisited the spatial representativity issue; it limits the realistic determination of biases associated with satellites (models). In one experiment, we convolved the kriging estimate for a multi-plume field with a box filter but various sizes. The perfect agreement (r=1.0) between the samples (point) and kriging output (pixel) seen at a high spatial resolution gradually vanished with coarsening of the resolution of grid boxes (r=0.8). We also directly compared samples (point) with pseudo satellite observations (showing the truth) with a coarse spatial resolution, which led to a flawed conclusion about the satellite being biased low. We modeled the semivariogram of those samples, estimated the field using kriging, and convolved with the pseudo satellite spatial response function. The direct comparison of this output with that of the satellite showed a completely different story, suggesting that the data were rather free of any bias. A serious caveat with using a spatial model (here kriging) is that it consists of errors: the estimations that are further from samples are less certain. It is widely known that discounting the measurement/model errors in true straight-line relationship between data can introduce artifacts. To consider the kriging variance in the comparisons we employed a Monte Carlo method on chi-square optimization, which ultimately allowed us to not only provide a set of solutions within the range of the uncertainty of the kriging model, but also to assign smaller weights on gross estimates.
We further validated monthly-averaged Ozone Monitoring Instrument (OMI) tropospheric NO2 columns using 11 Pandora spectrometer instrument (PSI) observations over Houston during NASA's DISCOVER-AQ campaign. A pixel-to-point comparison between two datasets suggested varying biases in OMI manifested in a slope far from the identity line. By contrast, the kriging estimate from the PSI measurements, convolved with the OMI spatial response function, resulted in an inter-comparison slope close to the unity line. This suggested that there was only a constant systematic bias ( molecules cm−2) associated with the OMI observations which does not vary with tropospheric NO2 column magnitudes.
The central component of satellite and model validation is pointwise measurements. Our experiments paved the way for a clear roadmap explaining how to transform these pointwise datasets to a comparable spatial scale relative to satellite (model) footprints. It is no longer necessary to ignore the problem of scale. The validation against point measurements can be carefully conducted in the following steps:
construct the experimental semivariogram if the number of point measurements allows (usually ≥3 within the field; the field can vary depending on the length scale of the compound);
drop the quantitative assessment if the number of point measurements are insufficient to gain spatial variance and the prior knowledge suggests a high likelihood of spatial heterogeneity within the field;
choose an appropriate function to model the semivariogram;
estimate the field with kriging (or any other spatial estimator capable of digesting the semivariogram) and calculate the variance;
find the optimum grid resolution of the estimate;
convolve the kriging estimate and its variance with the satellite (model) spatial response function (which is sensor-specific);
conduct the direct comparison of the convolved kriged output and the satellite (model) considering their errors through a Monte Carlo (or a weighted least-squares method).
Recent advances in satellite trace gas retrievals and atmospheric models have helped extend our understanding of atmospheric chemistry, but an important task before us in improving our knowledge on atmospheric composition is to embrace the semivariogram (or spatial autocorrelation) notion when it comes to validating satellites/models using pointwise measurements, so that we can have more robust quantitative applications of the data and models.
The analyses presented in this work utilized Schwanghart (2021a, b) functions in MATLAB.
Tropospheric NO2 columns from TROPOMI can be downloaded from https://disc.gsfc.nasa.gov/datasets/S5P_L2__NO2____HiR_1/summary (GES DISC, 2019). The surface Pandora spectrometer observations can be obtained from https://doi.org/10.5067/AIRCRAFT/DISCOVER-AQ/AEROSOL-TRACEGAS (NASA/LARC/SD/ASDC, 2014). OMI Tropospheric NO2 data refined with a regional model output are available upon the request from email@example.com.
The supplement related to this article is available online at: https://doi.org/10.5194/amt-15-41-2022-supplement.
AHS designed the research, executed the experiments, analyzed the data, made all figures, and wrote the paper. KS implemented the oversampling method, provided the spatial response functions, and oversampled TROPOMI data. KC, XL, and MSJ helped with the conceptualization of the study and the interpretation of the results. All authors contributed to discussions and edited the paper.
The contact author has declared that neither they nor their co-authors have any competing interests.
Publisher’s note: Copernicus Publications remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
Amir Souri and Matthew Johnson were funded for this work through NASA's Aura Science Team (grant no. 80NSSC21K1333). Kang Sun acknowledges support by NASA's Atmospheric Composition Modeling and Analysis (ACMAP) program (grant no. 80NSSC19K09). We thank many scientists whose concerns motivated us to tackle the presented problem. In particular, we thank Chris Chan Miller, Ron Cohen, Jeffrey Geddes, Gonzalo González Abad, Christian Hogrefe, Lukas Valin, and Huiqun (Helen) Wang.
This research has been supported by the National Aeronautics and Space Administration (grant nos. 80NSSC21K1333 and 80NSSC19K09).
This paper was edited by Can Li and reviewed by three anonymous referees.
Armstrong, M.: Is Research in Mining Geostats as Dead as a Dodo?, in: Geostatistics for the Next Century: An International Forum in Honour of Michel David's Contribution to Geostatistics, Montreal, 1993, edited by: Dimitrakopoulos, R., Springer Netherlands, Dordrecht, 303–312, https://doi.org/10.1007/978-94-011-0824-9_34, 1994.
Boersma, K. F., Eskes, H. J., Richter, A., De Smedt, I., Lorente, A., Beirle, S., van Geffen, J. H. G. M., Zara, M., Peters, E., Van Roozendael, M., Wagner, T., Maasakkers, J. D., van der A, R. J., Nightingale, J., De Rudder, A., Irie, H., Pinardi, G., Lambert, J.-C., and Compernolle, S. C.: Improving algorithms and uncertainty estimates for satellite NO2 retrievals: results from the quality assurance for the essential climate variables (QA4ECV) project, Atmos. Meas. Tech., 11, 6651–6678, https://doi.org/10.5194/amt-11-6651-2018, 2018.
Bryan, G. L.: Fluids in the universe: adaptive mesh refinement in cosmology, Comput. Sci. Eng., 1, 46–53, https://doi.org/10.1109/5992.753046, 1999.
Bucsela, E. J., Krotkov, N. A., Celarier, E. A., Lamsal, L. N., Swartz, W. H., Bhartia, P. K., Boersma, K. F., Veefkind, J. P., Gleason, J. F., and Pickering, K. E.: A new stratospheric and tropospheric NO2 retrieval algorithm for nadir-viewing satellite instruments: applications to OMI, Atmos. Meas. Tech., 6, 2607–2626, https://doi.org/10.5194/amt-6-2607-2013, 2013.
Chilès, J.-P. and Delfiner, P.: Geostatistics: Modeling Spatial Uncertainty, John Wiley & Sons, 718 pp., 2009.
Choi, S., Lamsal, L. N., Follette-Cook, M., Joiner, J., Krotkov, N. A., Swartz, W. H., Pickering, K. E., Loughner, C. P., Appel, W., Pfister, G., Saide, P. E., Cohen, R. C., Weinheimer, A. J., and Herman, J. R.: Assessment of NO2 observations during DISCOVER-AQ and KORUS-AQ field campaigns, Atmos. Meas. Tech., 13, 2523–2546, https://doi.org/10.5194/amt-13-2523-2020, 2020.
GES DISC: Sentinel-5P TROPOMI Tropospheric NO2 1-Orbit L2 5.5 km x 3.5 km, Greenbelt, MD, USA, Goddard Earth Sciences Data and Information Services Center (GES DISC) [data set], available at: https://disc.gsfc.nasa.gov/datasets/S5P_L2__NO2____HiR_1/summary (last access: 24 December 2021), 2019.
Goldberg, D. L., Saide, P. E., Lamsal, L. N., de Foy, B., Lu, Z., Woo, J.-H., Kim, Y., Kim, J., Gao, M., Carmichael, G., and Streets, D. G.: A top-down assessment using OMI NO2 suggests an underestimate in the NOx emissions inventory in Seoul, South Korea, during KORUS-AQ, Atmos. Chem. Phys., 19, 1801–1818, https://doi.org/10.5194/acp-19-1801-2019, 2019.
Herman, J., Cede, A., Spinei, E., Mount, G., Tzortziou, M., and Abuhassan, N.: NO2 column amounts from ground-based Pandora and MFDOAS spectrometers using the direct-sun DOAS technique: Intercomparisons and application to OMI validation, J. Geophys. Res., 114, D13307, https://doi.org/10.1029/2009JD011848, 2009.
Janjić, T., Bormann, N., Bocquet, M., Carton, J. A., Cohn, S. E., Dance, S. L., Losa, S. N., Nichols, N. K., Potthast, R., Waller, J. A., and Weston, P.: On the representation error in data assimilation, Q. J. Roy. Meteor. Soc., 144, 1257–1278, https://doi.org/10.1002/qj.3130, 2018.
Judd, L. M., Al-Saadi, J. A., Szykman, J. J., Valin, L. C., Janz, S. J., Kowalewski, M. G., Eskes, H. J., Veefkind, J. P., Cede, A., Mueller, M., Gebetsberger, M., Swap, R., Pierce, R. B., Nowlan, C. R., Abad, G. G., Nehrir, A., and Williams, D.: Evaluating Sentinel-5P TROPOMI tropospheric NO2 column densities with airborne and Pandora spectrometers near New York City and Long Island Sound, Atmos. Meas. Tech., 13, 6113–6140, https://doi.org/10.5194/amt-13-6113-2020, 2020.
Kendon, E. J., Roberts, N. M., Fowler, H. J., Roberts, M. J., Chan, S. C., and Senior, C. A.: Heavier summer downpours with climate change revealed by weather forecast resolution model, Nat. Clim. Change, 4, 570–576, https://doi.org/10.1038/nclimate2258, 2014.
Kim, H. C., Lee, S.-M., Chai, T., Ngan, F., Pan, L., and Lee, P.: A Conservative Downscaling of Satellite-Detected Chemical Compositions: NO2 Column Densities of OMI, GOME-2, and CMAQ, Remote Sens., 10, 1001, https://doi.org/10.3390/rs10071001, 2018.
Laughner, J. L., Zhu, Q., and Cohen, R. C.: The Berkeley High Resolution Tropospheric NO2 product, Earth Syst. Sci. Data, 10, 2069–2095, https://doi.org/10.5194/essd-10-2069-2018, 2018.
Li, R., Cui, L., Meng, Y., Zhao, Y., and Fu, H.: Satellite-based prediction of daily SO2 exposure across China using a high-quality random forest-spatiotemporal Kriging (RF-STK) model for health risk assessment, Atmos. Environ., 208, 10–19, https://doi.org/10.1016/j.atmosenv.2019.03.029, 2019.
Matheron, G.: Principles of geostatistics, Econ. Geol., 58, 1246–1266, https://doi.org/10.2113/gsecongeo.58.8.1246, 1963.
Mazzuca, G. M., Ren, X., Loughner, C. P., Estes, M., Crawford, J. H., Pickering, K. E., Weinheimer, A. J., and Dickerson, R. R.: Ozone production and its sensitivity to NOx and VOCs: results from the DISCOVER-AQ field experiment, Houston 2013, Atmos. Chem. Phys., 16, 14463–14474, https://doi.org/10.5194/acp-16-14463-2016, 2016.
Nowlan, C. R., Liu, X., Leitch, J. W., Chance, K., González Abad, G., Liu, C., Zoogman, P., Cole, J., Delker, T., Good, W., Murcray, F., Ruppert, L., Soo, D., Follette-Cook, M. B., Janz, S. J., Kowalewski, M. G., Loughner, C. P., Pickering, K. E., Herman, J. R., Beaver, M. R., Long, R. W., Szykman, J. J., Judd, L. M., Kelley, P., Luke, W. T., Ren, X., and Al-Saadi, J. A.: Nitrogen dioxide observations from the Geostationary Trace gas and Aerosol Sensor Optimization (GeoTASO) airborne instrument: Retrieval algorithm and measurements during DISCOVER-AQ Texas 2013, Atmos. Meas. Tech., 9, 2647–2668, https://doi.org/10.5194/amt-9-2647-2016, 2016.
Nowlan, C. R., Liu, X., Janz, S. J., Kowalewski, M. G., Chance, K., Follette-Cook, M. B., Fried, A., González Abad, G., Herman, J. R., Judd, L. M., Kwon, H.-A., Loughner, C. P., Pickering, K. E., Richter, D., Spinei, E., Walega, J., Weibring, P., and Weinheimer, A. J.: Nitrogen dioxide and formaldehyde measurements from the GEOstationary Coastal and Air Pollution Events (GEO-CAPE) Airborne Simulator over Houston, Texas, Atmos. Meas. Tech., 11, 5941–5964, https://doi.org/10.5194/amt-11-5941-2018, 2018.
Onn, F. and Zebker, H. A.: Correction for interferometric synthetic aperture radar atmospheric phase artifacts using time series of zenith wet delay observations from a GPS network, J. Geophys. Res., 111, B09102, https://doi.org/10.1029/2005JB004012, 2006.
Pan, S., Choi, Y., Roy, A., Li, X., Jeon, W., and Souri, A. H.: Modeling the uncertainty of several VOC and its impact on simulated VOC and ozone in Houston, Texas, Atmos. Environ., 120, 404–416, https://doi.org/10.1016/j.atmosenv.2015.09.029, 2015.
Pan, S., Choi, Y., Roy, A., and Jeon, W.: Allocating emissions to 4 km and 1 km horizontal spatial resolutions and its impact on simulated NOx and O3 in Houston, TX, Atmos. Environ., 164, 398–415, https://doi.org/10.1016/j.atmosenv.2017.06.026, 2017a.
Pan, S., Choi, Y., Jeon, W., Roy, A., Westenbarger, D. A., and Kim, H. C.: Impact of high-resolution sea surface temperature, emission spikes and wind on simulated surface ozone in Houston, Texas during a high ozone episode, Atmos. Environ., 152, 362–376, https://doi.org/10.1016/j.atmosenv.2016.12.030, 2017b.
Platt, U., Wagner, T., Kuhn, J., and Leisner, T.: The “ideal” spectrograph for atmospheric observations, Atmos. Meas. Tech., 14, 6867–6883, https://doi.org/10.5194/amt-14-6867-2021, 2021.
Pyrcz, M. J. and Deutsch, C. V.: The whole story on the hole effect, Geostatistical Association of Australasia, Newsletter, 18, 3–5, May 2003.
Rennen, G.: Subset Selection from Large Datasets for Kriging Modeling, CentER Discussion Paper Series No. 2008-26, Social Science Research Network [data set], Rochester, NY, https://doi.org/10.2139/ssrn.1104595, 2008.
Russell, A. R., Perring, A. E., Valin, L. C., Bucsela, E. J., Browne, E. C., Wooldridge, P. J., and Cohen, R. C.: A high spatial resolution retrieval of NO2 column densities from OMI: method and evaluation, Atmos. Chem. Phys., 11, 8543–8554, https://doi.org/10.5194/acp-11-8543-2011, 2011.
Schwanghart, W.: variogramfit, MATLAB Central File Exchange [code], available at: https://www.mathworks.com/matlabcentral/fileexchange/25948-variogramfit, last access: 24 December 2021a.
Schwanghart, W.: Ordinary Kriging, MATLAB Central File Exchange [code], available at: https://www.mathworks.com/matlabcentral/fileexchange/29025-ordinary-kriging, last access: 24 December 2021b.
Shah, V., Jacob, D. J., Li, K., Silvern, R. F., Zhai, S., Liu, M., Lin, J., and Zhang, Q.: Effect of changing NOx lifetime on the seasonality and long-term trends of satellite-observed tropospheric NO2 columns over China, Atmos. Chem. Phys., 20, 1483–1495, https://doi.org/10.5194/acp-20-1483-2020, 2020.
Souri, A. H., Choi, Y., Jeon, W., Li, X., Pan, S., Diao, L., and Westenbarger, D. A.: Constraining NOx emissions using satellite NO2 measurements during 2013 DISCOVER-AQ Texas campaign, Atmos. Environ., 131, 371–381, https://doi.org/10.1016/j.atmosenv.2016.02.020, 2016.
Souri, A. H., Choi, Y., Pan, S., Curci, G., Nowlan, C. R., Janz, S. J., Kowalewski, M. G., Liu, J., Herman, J. R., and Weinheimer, A. J.: First Top-Down Estimates of Anthropogenic NOx Emissions Using High-Resolution Airborne Remote Sensing Observations, J. Geophys. Res.-Atmos., 123, 3269–3284, https://doi.org/10.1002/2017JD028009, 2018.
Souri, A. H., Choi, Y., Kodros, J. K., Jung, J., Shpund, J., Pierce, J. R., Lynn, B. H., Khain, A., and Chance, K.: Response of Hurricane Harvey's rainfall to anthropogenic aerosols: A sensitivity study based on spectral bin microphysics with simulated aerosols, Atmos. Res., 242, 104965, https://doi.org/10.1016/j.atmosres.2020.104965, 2020a.
Souri, A. H., Nowlan, C. R., Wolfe, G. M., Lamsal, L. N., Chan Miller, C. E., Abad, G. G., Janz, S. J., Fried, A., Blake, D. R., Weinheimer, A. J., Diskin, G. S., Liu, X., and Chance, K.: Revisiting the effectiveness of HCHO NO2 ratios for inferring ozone sensitivity to its precursors using high resolution airborne remote sensing observations in a high ozone episode during the KORUS-AQ campaign, Atmos. Environ., 224, 117341, https://doi.org/10.1016/j.atmosenv.2020.117341, 2020b.
Sun, K., Zhu, L., Cady-Pereira, K., Chan Miller, C., Chance, K., Clarisse, L., Coheur, P.-F., González Abad, G., Huang, G., Liu, X., Van Damme, M., Yang, K., and Zondlo, M.: A physics-based approach to oversample multi-satellite, multispecies observations to a common grid, Atmos. Meas. Tech., 11, 6679–6701, https://doi.org/10.5194/amt-11-6679-2018, 2018.
Swall, J. L. and Foley, K. M.: The impact of spatial correlation and incommensurability on model evaluation, Atmos. Environ., 43, 1204–1217, https://doi.org/10.1016/j.atmosenv.2008.10.057, 2009.
Tadić, J. M., Michalak, A. M., Iraci, L., Ilić, V., Biraud, S. C., Feldman, D. R., Bui, T., Johnson, M. S., Loewenstein, M., Jeong, S., Fischer, M. L., Yates, E. L., and Ryoo, J.-M.: Elliptic Cylinder Airborne Sampling and Geostatistical Mass Balance Approach for Quantifying Local Greenhouse Gas Emissions, Environ. Sci. Technol., 51, 10012–10021, https://doi.org/10.1021/acs.est.7b03100, 2017.
Tang, W., Edwards, D. P., Emmons, L. K., Worden, H. M., Judd, L. M., Lamsal, L. N., Al-Saadi, J. A., Janz, S. J., Crawford, J. H., Deeter, M. N., Pfister, G., Buchholz, R. R., Gaubert, B., and Nowlan, C. R.: Assessing sub-grid variability within satellite pixels over urban regions using airborne mapping spectrometer measurements, Atmos. Meas. Tech., 14, 4639–4655, https://doi.org/10.5194/amt-14-4639-2021, 2021.
Valin, L. C., Russell, A. R., Hudman, R. C., and Cohen, R. C.: Effects of model resolution on the interpretation of satellite NO2 observations, Atmos. Chem. Phys., 11, 11647–11655, https://doi.org/10.5194/acp-11-11647-2011, 2011.
Vinken, G. C. M., Boersma, K. F., Jacob, D. J., and Meijer, E. W.: Accounting for non-linear chemistry of ship plumes in the GEOS-Chem global chemistry transport model, Atmos. Chem. Phys., 11, 11707–11722, https://doi.org/10.5194/acp-11-11707-2011, 2011.
Wang, P., Piters, A., van Geffen, J., Tuinder, O., Stammes, P., and Kinne, S.: Shipborne MAX-DOAS measurements for validation of TROPOMI NO2 products, Atmos. Meas. Tech., 13, 1413–1426, https://doi.org/10.5194/amt-13-1413-2020, 2020.
Wang, Y., Sabatino, S. D., Martilli, A., Li, Y., Wong, M. S., Gutiérrez, E., and Chan, P. W.: Impact of land surface heterogeneity on urban heat island circulation and sea-land breeze circulation in Hong Kong, J. Geophys. Res.-Atmos., 122, 4332–4352, https://doi.org/10.1002/2017JD026702, 2017.
Wolfe, G. M., Nicely, J. M., Clair, J. M. S., Hanisco, T. F., Liao, J., Oman, L. D., Brune, W. B., Miller, D., Thames, A., Abad, G. G., Ryerson, T. B., Thompson, C. R., Peischl, J., McKain, K., Sweeney, C., Wennberg, P. O., Kim, M., Crounse, J. D., Hall, S. R., Ullmann, K., Diskin, G., Bui, P., Chang, C., and Dean-Day, J.: Mapping hydroxyl variability throughout the global remote troposphere via synthesis of airborne and satellite formaldehyde observations, P. Natl. Acad. Sci., 116, 11171–11180, https://doi.org/10.1073/pnas.1821661116, 2019.
Wu, C.-D., Zeng, Y.-T., and Lung, S.-C. C.: A hybrid kriging/land-use regression model to assess PM2.5 spatial-temporal variability, Sci. Total Environ, 645, 1456–1464, https://doi.org/10.1016/j.scitotenv.2018.07.073, 2018.
Yu, K., Jacob, D. J., Fisher, J. A., Kim, P. S., Marais, E. A., Miller, C. C., Travis, K. R., Zhu, L., Yantosca, R. M., Sulprizio, M. P., Cohen, R. C., Dibb, J. E., Fried, A., Mikoviny, T., Ryerson, T. B., Wennberg, P. O., and Wisthaler, A.: Sensitivity to grid resolution in the ability of a chemical transport model to simulate observed oxidant chemistry under high-isoprene conditions, Atmos. Chem. Phys., 16, 4369–4378, https://doi.org/10.5194/acp-16-4369-2016, 2016.
Zhan, Y., Luo, Y., Deng, X., Zhang, K., Zhang, M., Grieneisen, M. L., and Di, B.: Satellite-Based Estimates of Daily NO2 Exposure in China Using Hybrid Random Forest and Spatiotemporal Kriging Model, Environ. Sci. Technol., 52, 4180–4189, https://doi.org/10.1021/acs.est.7b05669, 2018.
Zhao, X., Griffin, D., Fioletov, V., McLinden, C., Cede, A., Tiefengraber, M., Müller, M., Bognar, K., Strong, K., Boersma, F., Eskes, H., Davies, J., Ogyu, A., and Lee, S. C.: Assessment of the quality of TROPOMI high-spatial-resolution NO2 data products in the Greater Toronto Area, Atmos. Meas. Tech., 13, 2131–2159, https://doi.org/10.5194/amt-13-2131-2020, 2020.