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Downscaled High Resolution Datasets for Climate Change Projections

Global climate models (GCMs) have generated projections of temperature, precipitation and other important climate change parameters with spatial resolutions of 100 to 300 km. However, higher spatial resolution information is required to assess threats to individual installations or regions. A variety of “downscaling” approaches have been used to produce high spatial resolution output (datasets) from the global climate models at scales that are useful for evaluating potential threats to critical infrastructure at regional and local scales. These datasets enable development of information about projections produced from various climate models, about downscaling to achieve desired locational specificity, and about selecting the appropriate dataset(s) to use for performing specific assessments. This article describes how these datasets can be accessed and used to evaluate potential climate change impacts.

Related Article(s):

Contributor(s): Dr. Rao Kotamarthi

Key Resource(s):

  • Use of Climate Information for Decision-Making and Impacts Research: State of our Understanding[1]
  • Applying Climate Change Information to Hydrologic and Coastal Design of Transportation Infrastructure, Design Practices[2]
  • Statistical Downscaling and Bias Correction for Climate Research[3]
  • Downscaling Techniques for High-Resolution Climate Projections: From Global Change to Local Impacts[4]

Downscaling of Global Climate Models

Some communities and businesses have begun to improve their resilience to climate change by building adaptation plans based on national scale climate datatsets (National Adaptation Plans), regional datasets (New York State Flood Risk Management Guidance[5]), and datasets generated at local spatial resolutions. Resilience to the changing climate has also been identified by the US Department of Defense (DoD) as a necessary part of the installation planning and basing process (https://media.defense.gov/2019/Jan/29/2002084200/-1/-1/1/CLIMATE-CHANGE-REPORT-2019.PDF DoD Report on Effects of a Changing Climate][6]). More than 79 installations were identified as facing potential threats from climate change. The threats faced due to changing climate include recurrent flooding, droughts, desertification, wildfires and thawing permafrost.

Assessing the threats climate change poses at regional and local scales requires data with higher spatial resolution than is currently available from global climate models. Global-scale climate models typically have spatial resolutions of 100 to 300 km, and output from these models needs to be spatially and/or temporally disaggregated in order to be useful in performing assessments at smaller scales. The process of producing higher spatial-temporal resolution climate model output from coarser global climate model outputs is referred to as “downscaling” and results in climate change projections (datasets) at scales that are useful for evaluating potential threats to regional and local communities and businesses. These datasets provide information on temperature, precipitation and a variety of other climate variables for current and future climate conditions under various greenhouse gas (GHG) emission scenarios. There are a variety of web-based tools available for accessing these datasets to evaluate potential climate change impacts at regional and local scales.

Methods for Downscaling

There are two main approaches to downscaling. One method, commonly referred to as “statistical downscaling”, uses the empirical-statistical relationships between large-scale weather phenomena and historical local weather data. In this method, these statistical relationships are applied to output generated by global climate models. A second method uses physics-based numerical models (regional-scale climate models or RCMs) of weather and climate that operate over a limited region of the earth (e.g., North America) and at spatial resolutions that are typically 3 to 10 times finer than the global-scale climate models. This method is known as “dynamical downscaling”. These regional-scale climate models are similar to the global models with respect to their reliance on the principles of physics, but because they operate over only part of the earth, they require information about what is coming in from the rest of the earth as well as what is going out of the limited region of the model. This is generally obtained from a global model. The primary differences between statistical and dynamical downscaling methods are summarized in Table 1.

Table 1. Two widely used methods for developing downscaled higher resolution climate model projections
Dynamical Downscaling Statistical Downscaling
Deterministic climate change simulations that output many climate variables with sub-daily information Primarily limited to daily temperature and precipitation
Computationally expensive; hence, limited number of simulations – both GHG emission scenarios and global climate models downscaled Computationally efficient; hence, downscaled data typically available for many different global climate models and GHG emission scenarios
May require additional bias correction Method incorporates bias correction
Observational data at the downscaled location are not necessary to obtain the downscaled output at the location Best suited for locations with 30 years or more of observational data
Does not assume stationarity or in other words the model simulates the future regardless of what has happened in the past Stationarity assumption - assumes that the statistical relationship between global climate model and observations will remain constant in the future


Figure 1. A representation of a clam living in a sediment bed that contains a chemical contaminant (depicted as red hexagons). The contaminant is partly dissolved in the sediment porewater between the solid grains, and partly associated with solid phases, like natural organic matter and "black carbons" such as soots from diesel engines and chars emitted during forest fires. All of these liquid and solid materials can exchange their contaminant loads with one another, with the distributions dependent on the chemical's relative affinity for each material. When an animal like the clam moves into this system, the chemical is also accumulated into the animal, until the animal is also equilibrated with the other solids and liquid(s) present.

Environmental media such as sediments typically contain many different materials or phases, including liquid solutions (e.g. water, nonaqueous phase liquids like spilled oils) and diverse solids (e.g., quartz, aluminosilicate clays, and combustion-derived soots). Further, the chemical concentration in the porewater medium includes both molecules that are "truly dissolved" in the water and others that are associated with colloids in the porewater[7][8][9]. As a result, contaminant chemicals distribute among these diverse media (Figure 1) according to their affinity for each and the amount of each phase in the system[10][11][12][13][14]. As such, the chemical concentration in any one medium (e.g., truly dissolved in porewater) in a multi-material system like sediment is very hard to know from measures of the total sediment concentration, which unfortunately is the information typically found by analyzing for chemicals in sediment samples.

If an animal moves into this system, it will also accumulate the chemical in its tissues from the loads in all the other materials (Figure 1). This can lead to exposures of the chemical to other organisms, including humans, who may eat such animals. Predicting the quantity of contaminant in the animal requires knowledge of the relative affinities of the chemical for the animal versus the sediment materials. For example, if one knew the chemical's truly dissolved concentration in the porewater and could reasonably assume the chemical of interest in the animal has mostly accumulated in its lipids (as is often the case for very hydrophobic compounds), then one could estimate the chemical concentration in the animal (Canimal, typically in units of μg/kg animal wet weight) using a lipid-water partition coefficient, Klipid-water, typically in units of (μg/kg lipid)/(μg/L water), and the porewater concentration of the chemical (Cporewater, in μg/L) with Equation 1.

Equation 1. Canimal = flipid x Klipid-water x Cporewater
where:
flipid is the fraction lipids contribute to the total wet weight of the animal (kg lipid/kg animal wet weight), and
Cporewater is the freely dissolved contaminant concentration in the porewater surrounding the animal.

While there is a great deal of information on the values of Klipid-water for many chemicals[15], it is often very inaccurate to estimate truly dissolved porewater concentrations from total sediment concentrations using assumptions about the affinity of those chemicals for the solids in the system[10]. Further, it is difficult to isolate porewater without colloids and/or measure the very low truly dissolved concentrations of hydrophobic contaminants of concern like polycyclic aromatic hydrocarbons (PAHs), polychlorinated biphenyls (PCBs), nonionic pesticides like dichlorodiphenyltrichloroethane (DDT), and polychlorinated dibenzo-p-dioxins (PCDDs)/ dibenzofurans (PCDFs)[16].

Passive Samplers

One approach to address this problem for contaminated sediments is to insert into the sediment billets of organic polymers like low density polyethylene (LDPE), polydimethylsiloxane (PDMS), or polyoxymethylene (POM) that can absorb such hydrophobic chemicals from their surroundings[17][18][19][20][21][22][23]. In this approach, the polymer is inserted in the sediment bed where it absorbs some of the contaminant load via the contaminant's diffusion into the polymer from the surroundings. When the polymer achieves sorptive equilibration with the sediments, the chemical concentration in the polymer, Cpolymer (μg/kg polymer), can be used to find the corresponding concentration in the porewater, Cporewater (μg/L), using a polymer-water partition coefficient, Kpolymer-water ((μg/kg polymer)/(μg/L water)), that has previously been found in laboratory testing[24][25], as shown in Equation 2.

         Equation 2. Cporewater = Cpolymer / Kpolymer-water

Such “passive uptake” by the polymer also reflects the availability of the chemicals for transport to adjacent systems (e.g., overlying surface waters) and for uptake into organisms (e.g., bioaccumulation). Thus, one can use the porewater concentrations to estimate the biotic accumulation of the chemicals, too. For example, for the concentration in the animal equilibrated with the sediment, Canimal (μg/kg animal), would be found by combining Equations 1 and 2 to get Equation 3.

         Equation 3. Canimal = flipid x Klipid-water x Cpolymer / Kpolymer-water
Figure 2a. Plot of the initial concentrations of a PRC (green lines) in a polyethylene (PE) sheet inserted in a sediment showing constant concentration across the PE and zero concentration outside the PE. At the same time, a target contaminant of interest (red lines) initially has a constant concentration in the sediment outside the PE and zero concentration inside the PE.
Figure 2b. After the PE has been deployed for a time, the PRC is depleted from the PE (green lines), especially near the surfaces contacting the sediment, and its concentration is building up outside the PE and diffusing away into the sediment. Meanwhile, the target chemical leaves the sediment and begins to diffuse into the PE (red lines). The "jumps" in concentration at the PE-sediment boundary reflect the equilibrium paritioning coefficient,
KPE-sed = CPE / Csediment.

Performance Reference Compounds (PRCs)

Perhaps unsurprisingly, pollutants with low water solubility like PAHs, PCBs, etc. do not diffuse quickly through sediment beds. As a result, their accumulation in polymeric materials in sediments can take a long time to achieve equilibration[26][27][28]. This problem was recognized previously for passive samplers called semipermeable membrane devices (SPMDs, e.g. polyethylene bags filled with triolein[29]) that were deployed in surface waters. As a result, representative chemicals called performance reference compound (PRCs) were dosed inside the samplers before their deployment in the environment, and the PRCs' diffusive losses out of the SPMD could be used to quantify the fractional approach toward sampler-environmental surroundings equilibration[30][29]. A similar approach can be used for polymers inserted in sediment beds[26][31]. Commonly, isotopically labeled forms of the compounds of interest such as deuterated or 13C-labelled PAHs or PCBs are homogeneously impregnated into the polymers before their deployments. Upon insertion of the polymer into the sediment bed (or overlying waters or even air), the initially evenly distributed PRCs begin to diffuse out of the sampling polymer and into the surroundings (Figure 2).

Assuming the contaminants of interest undergo the same mass transfer restrictions limiting their rates of uptake into the polymer (e.g., diffusion through the sedimentary porous medium) that are also limiting transfers of the PRCs out of the polymer[26][31], then fractional losses of the PRCs during a particular deployment can be used to adjust the accumulated contaminant loads to what they would have been at equilibrium with their surroundings with Equation 4.

Equation 4. C(∞)polymer = C(t)polymer / fPRC lost
where:
fPRC lost is the fraction of the PRC lost to outward diffusion,
C(∞)polymer is the concentration of the contaminant in the polymer at equilibrium, and
C(t)polymer is the concentration of the contaminant in the polymer after deployment time, t.                     

Since investigators are commonly interested in many chemicals at the same time, it is impractical to have a PRC for each contaminant of interest. Instead, a representative set of PRCs is used to characterize the rates of polymer-environment exchange as a function of the PRCs' properties (e.g., diffusivities, partition coefficients), the sediments characteristics (e.g., porosity), and the nature of the polymer used (e.g., film thickness, affinity for the chemicals)[26][27]. The resulting mass transfer model fit can then be used to estimate the fractional approaches to equilibrium for many other contaminants, whose diffusive and partitioning properties are also known. And these fractions can be used to adjust the target chemical concentrations that have accumulated from the sediment into the same polymeric sampler to find the equilibrated results[31]. Finally, these equilibrated concentrations can be used in Eq. 2 to estimate truly dissolved contaminant concentrations in the sediment's porewater.

Field Applications

Figure 3. Passive sampler system made of polyethylene sheet loaded into an aluminum sheet metal frame, before (left), during (middle), and after (right) deployment in sediment.

Polymeric materials can be deployed in sediment in various ways[32]. PDMS coatings can be incorporated into slotted silica rods called SPMEs (solid phase micro extraction devices), while thin sheets of polymers like LDPE or POM can be incorporated into sheet metal frames. In both cases, such hardware is used to insert the polymers into sediment beds (Figure 3).

Deployment of the assembled passive samplers can be accomplished via poles from a boat[31], by divers[23], or by attaching the samplers to a sampling platform lowered off a vessel[33]. Typically, the method used depends on the water depth. Small buoys on short lines, sometimes with associated water-sampling polymeric materials in mesh bags (see right panel of Figure 3), are attached to the samplers to facilitate the sampler recoveries. After recovery, the samplers are wiped to remove any adhering sediment, biofilm, or precipitates and returned to the laboratory for PRC and target contaminant analyses. The resulting measurements of the accumulated target chemical concentrations can be adjusted using the observed PRC losses and publicly available software programs[34][35].

Subsequently, since the passive sampling reveals the concentrations of contaminants in a sediment bed's porewater and the overlying bottom water[18], the data can be used to estimate bed-to-water column diffusive fluxes of contaminants[36][33] and bioirrigation-affected fluxes[37]. The data are also useful for assessing the tendency of the contaminants to accumulate in benthic organisms[38][39][40], and by extension into food webs that include such benthic species[41]. Furthermore, recent efforts have found that passive sampling observations can be used to infer in situ transformations of substances like nitro aromatic compounds[42] and DDT[43].


References

  1. ^ Kotamarthi, R., Mearns, L., Hayhoe, K., Castro, C.L., and Wuebble, D., 2016. Use of Climate Information for Decision-Making and Impacts Research: State of Our Understanding. Department of Defense, Strategic Environmental Research and Development Program (SERDP), 55pp. Free download from: SERDP-ESTCP
  2. ^ Kilgore, R., Thomas, W.O. Jr., Douglass, S., Webb, B., Hayhoe, K., Stoner, A., Jacobs, J.M., Thompson, D.B., Herrmann, G.R., Douglas, E., and Anderson, C., 2019. Applying Climate Change Information to Hydrologic and Coastal Design of Transportation Infrastructure, Design Practices. The National Cooperative Highway Research Program, Transportation Research Board, Project 15-61, 154 pages. Free download from: The Transportation Research Board
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  32. ^ Cite error: Invalid <ref> tag; no text was provided for refs named Burgess2017
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  43. ^ Tcaciuc, A.P., Borrelli, R., Zaninetta, L.M., and Gschwend, P.M., 2018. Passive sampling of DDT, DDE and DDD in sediments: accounting for degradation processes with reaction–diffusion modeling. Environmental Science: Processes and Impacts, 20(1), pp. 220-231. DOI: 10.1039/C7EM00501F   Open access article available from: Royal Society of Chemistry.

See Also

A PRC Correction Calculator for LDPE deployed in sediments

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