Advocating for Science: Amici Curiae Brief of Wetland and Water Scientists in Support of the Clean Water Rule

Wetlands, May 2019

The Trump administration has proposed replacing the Clean Water Rule, a 2015 regulation that defined the statutory term “waters of the United States” to clarify the geographic jurisdiction of the Clean Water Act. Since its promulgation, the Clean Water Rule has been subjected to numerous judicial challenges. We submitted an amici curiae brief to the United States Court of Appeals for the Sixth Circuit, explaining why the Clean Water Rule, and its definition of “waters of the United States,” is scientifically sound. The definition of “waters of the United States” is a legal determination informed by science. The best available science supports the Clean Water Rule’s categorical treatment of tributaries because compelling scientific evidence demonstrates that tributaries significantly affect the chemical, physical, and biological integrity of traditional navigable waters (primary waters). Similarly, the best available science supports the Clean Water Rule’s categorical treatment of adjacent waters based on geographic proximity. Compelling scientific evidence demonstrates that waters within 100 ft of an ordinary high water mark (OHWM) significantly affect the chemical, physical, and biological integrity of primary waters, as do waters within 100-year floodplains and waters within 1500 ft of high tide lines of tidally influenced primary waters or OHWMs of the Great Lakes. This review article is adapted from that amici brief.

A PDF file should load here. If you do not see its contents the file may be temporarily unavailable at the journal website or you do not have a PDF plug-in installed and enabled in your browser.

Alternatively, you can download the file locally and open with any standalone PDF reader:

Advocating for Science: Amici Curiae Brief of Wetland and Water Scientists in Support of the Clean Water Rule

Wetlands pp 1–12 | Cite as Advocating for Science: Amici Curiae Brief of Wetland and Water Scientists in Support of the Clean Water Rule AuthorsAuthors and affiliations Royal C. GardnerErin OkunoSteph TaiM. Siobhan FennessyCarol A. JohnstonMarinus L. OtteMargaret PalmerJames E. PerryCharles SimenstadBenjamin R. TannerDan TuffordR. Eugene TurnerKirsten WorkScott C. YaichJoy B. Zedler Open Access General Wetland Science First Online: 22 May 2019 2 Shares Abstract The Trump administration has proposed replacing the Clean Water Rule, a 2015 regulation that defined the statutory term “waters of the United States” to clarify the geographic jurisdiction of the Clean Water Act. Since its promulgation, the Clean Water Rule has been subjected to numerous judicial challenges. We submitted an amici curiae brief to the United States Court of Appeals for the Sixth Circuit, explaining why the Clean Water Rule, and its definition of “waters of the United States,” is scientifically sound. The definition of “waters of the United States” is a legal determination informed by science. The best available science supports the Clean Water Rule’s categorical treatment of tributaries because compelling scientific evidence demonstrates that tributaries significantly affect the chemical, physical, and biological integrity of traditional navigable waters (primary waters). Similarly, the best available science supports the Clean Water Rule’s categorical treatment of adjacent waters based on geographic proximity. Compelling scientific evidence demonstrates that waters within 100 ft of an ordinary high water mark (OHWM) significantly affect the chemical, physical, and biological integrity of primary waters, as do waters within 100-year floodplains and waters within 1500 ft of high tide lines of tidally influenced primary waters or OHWMs of the Great Lakes. This review article is adapted from that amici brief. KeywordsClean Water Act Waters of the United States Wetlands Navigable waters Significant nexus Regulation  Dan Tufford and Scott C. Yaich are both retired. The Clean Water Act (CWA) (2018) is the primary wetland protection law in the United States (33 U.S.C. §1251 et seq.). If a wetland is considered to be “waters of the United States” under the CWA, then no one may discharge pollutants into that wetland without a federal permit. The geographic scope of the Clean Water Act—i.e., the extent of waters of the United States—has long been subject to controversy and litigation (Gardner 2011). In 2015, the Obama administration issued the Clean Water Rule, a regulation that clarified the geographic scope of the CWA (U.S. Army Corps of Engineers and U.S. EPA 2015). This regulation was based upon an analysis of over 1200 scientific publications in Connectivity of Streams and Wetlands to Downstream Waters: A Review and Synthesis of the Scientific Evidence (U.S. EPA Office of Research and Development 2015). This analysis was performed to comply with the Administrative Procedure Act (2018), which prohibits federal agencies from acting arbitrarily or capriciously (5 U.S.C. §706). Courts have interpreted this language to require agencies to consider the scientific basis behind their decisions (see, e.g., Motor Vehicle Mfrs. Ass’n v. State Farm Mut. Auto. Ins. Co., 463 U.S. 29 (1983), which mandates that agencies “articulate a satisfactory explanation for [their] action[s],” provide a “reasoned analysis” for their decisions, consider all “relevant factors” in reaching their decisions, and explore “alternative ways of achieving” the purpose of their rules). Nevertheless, the Clean Water Rule was immediately challenged by industry groups and others on procedural, statutory, and constitutional grounds. A major claim—raised under the Administrative Procedure Act—was that the U.S. Environmental Protection Agency (EPA) and the U.S. Army Corps of Engineers (Corps) failed to adequately provide scientific support for the regulation, thereby rendering it arbitrary and capricious.1 In January 2017, the authors, a group of twelve wetland and water scientists and their attorneys, filed an amici curiae brief in the United States Court of Appeals for the Sixth Circuit in support of the scientific basis behind the Clean Water Rule. An objective of the amici brief was to educate the court about basic wetland and water science. Since then, the debate over what constitutes waters of the United States has become more complicated through a series of Trump administration rulemakings and judicial decisions (Gardner and Okuno 2018). In February 2018, the Trump administration attempted to suspend the Clean Water Rule for 2 years and, in doing so, expressly refused to consider the scientific basis on the Clean Water Rule (U.S. Army Corps of Engineers and U.S. EPA 2018a). In December 2018, the Trump administration announced its intent to replace the Clean Water Rule with a more restrictive definition of waters of the United States, again diminishing the importance of science (U.S. Army Corps of Engineers and U.S. EPA 2018b). In this context, we believe it is critical to emphasize the importance of science in CWA rulemaking. As professionals who have spent their careers studying streams, wetlands, and other aquatic ecosystems, the amici and their attorneys have long explored the ways in which human activities that affect one part of a watershed can also affect—and damage—other parts of that watershed. In doing so, the amici have applied the basic tools of the profession: literature review, on-site observations, measurements, experimental manipulations, studies of “natural experiments,” and modeling based on observations and understanding of the physical sciences. Based upon these tools, we believe that current science provides sound support for the Clean Water Rule. In this review, which is adapted from our brief (and supplemented with additional studies), we elaborate on the scientific basis behind efforts to address human activities that alter the integrity of aquatic ecosystems. Damage to these systems can affect society in a number of ways, including: harming human welfare and property via flooding; impairing human health and reducing recreational opportunities via water pollution; and threatening species, including commercial species harvested in fisheries, via water pollution and a loss of connectivity (Sarukhán et al. 2005; Pendleton 2008; Moreno-Mateos and Palmer 2016; Gardner and Finlayson 2018). We believe that the Clean Water Rule’s definition of “waters of the United States” is a scientifically justified approach to address these impacts. The Clean Water Rule Is Scientifically Sound In drafting the Clean Water Rule, the EPA and the Corps utilized many methodologies commonly employed by wetland and water scientists. The agencies studied key chemical, physical, and biological features of water systems and relied upon studies that used rigorous and respected methodologies in researching aquatic ecosystems. Key Chemical, Physical, and Biological Features Are Used to Study Water Systems An early major National Research Council report, Wetlands: Characteristics and Boundaries, which amici Joy Zedler and Carol Johnston co-authored, outlined three structural components of wetlands that apply generally to all water systems: water, substrate (physical and chemical features), and biota (animals, plants, and microorganisms) (National Research Council 1995). Each component interacts with the others to shape the functions (services) of water systems. In the study underlying the Clean Water Rule, the EPA and the Corps examined connections among the three components to provide an integrated, scientific perspective on water systems (U.S. EPA Office of Research and Development 2015). Rigorous Research Methods Are Used to Study these Attributes, and to Study Aquatic Ecosystems as a Whole The study of water systems integrates several scientific disciplines. In the context of understanding wetlands, hydrology, geology, and chemistry are used to examine how wetlands regulate stream flow, filter pollutants and sediment, incorporate excess nutrients, act to control flooding, and connect to groundwater (see, e.g., Johnston 1991; Hey and Philippi 2006; Hancock et al. 2009). Ecological research can be used to examine the role of wetlands as habitats for fish and wildlife, and their support of food webs within and among interconnected water systems (see, e.g., Sierszen et al. 2012b; Gray et al. 2013). Underlying this cross-disciplinary approach is a focus on the various methodologies noted above. Scientists do not apply these methods independently of each other, but rather actively compare them to ensure that the results are robust and reproducible (cf. Goodstein 2011). To study water systems, scientists use a wide range of sampling and analytical methods to make on-site observations and measurements (see DeLaune et al. 2013). These methods include examining the chemical and physical characteristics of the waters, characterizing soil and sediment samples, sampling plant and animal communities, and quantifying the direction and movement of water and materials (dissolved and particulate) in stream networks and to/from wetlands (see generally DeLaune et al. 2013; see also Kondolf and Piégay 2016). These sampling and analytical methods are well-established, rigorous, and refined over time; they are used to enhance scientific understanding of the relationships between the various components of water systems. Watershed or hydrologic studies may make use of “natural experiments” (a form of observational study), which focus on comparing a natural event or feature with areas (or times) with and without the event or feature (Breyer et al. 2011; see also Layzer 2008). In studying developed and undeveloped watersheds, for example, the assignment of subjects (e.g., watersheds) to groups (e.g., developed or not) is akin to randomization. Such natural experiments are often necessary because ethical considerations (i.e., concerns of deliberately damaging those systems), size, and cost create barriers for actual experiments on existing systems (see Haack 2003). Rather than disrupting existing systems, scientists focus on variability to extrapolate the effects of differences on the overall water system. Scientists who study freshwater ecosystems also use naturally occurring and injected tracers that do not cause any harm to the system but move with the water and allow us to identify the direction and magnitude of water transport as well as the rates of many ecological processes (Mulholland et al. 1990; Bertrand et al. 2014; Martínez-Carreras et al. 2015). This has been increasingly important in documenting flow paths and connectivity and the role of systems in global biogeochemical cycles (Abbott et al. 2016). Leibowitz et al. (2018) provide an extensive review of hydrologic connectivity and describe field-based, modeling, and remote sensing methods to detect stream and wetland connectivity to downstream waters. Rinderer et al. (2018) provide a detailed overview of the mathematics and statistics useful for assessing connectivity from time-series of groundwater and streamflow. Modeling approaches also enhance scientific understanding of the water-system relationships (see National Judicial College 2010, describing computer-based models as “essential” for understanding water systems). Models serve multiple purposes. First, they enable scientists to test their understanding of interrelationships between different components of a water system (National Judicial College 2010). Second, they enable scientists to predict the outcomes of potential human activities that may cause damage—without modifying those systems (National Judicial College 2010). Models also make it possible to study processes at scales ranging from watersheds to continents that are too extensive to be investigated by observations alone, and to simulate scenarios of hydrologic and other wetland/watershed processes drawn from the historical record (e.g., Wu and Johnston 2008). A number of modeling tools are directly relevant to advancing scientific understanding of hydrologic connectivity between isolated wetlands and surface waters (Golden et al. 2014; Jones et al. 2018). As noted above, the Clean Water Rule was based on, inter alia, an analysis entitled Connectivity of Streams and Wetlands to Downstream Waters: A Review and Synthesis of the Scientific Evidence (U.S. EPA Office of Research and Development 2015), which considered over 1200 scientific publications. The Connectivity Report reached its conclusions using studies that applied all of these methodologies. Indeed, the EPA, in its Connectivity Report, compiled these studies in a manner to ensure the use of high-quality, relevant research (U.S. EPA Office of Research and Development 2015; see also U.S. EPA and U.S. Department of the Army 2015, describing the extensive process of peer review of the Connectivity Report itself, including the use of a panel of 27 technical experts from an array of relevant fields, as well as other public processes). Moreover, the Connectivity Report included only studies that were peer reviewed or otherwise verified for quality assurance (U.S. EPA Office of Research and Development 2015; U.S. EPA and U.S. Department of the Army 2015). The focus on high standards and verification through peer review means that the Connectivity Report used the best available science to develop the Clean Water Rule (see 80 Federal Register 37,054; see also, e.g., Sullivan et al. 2006, describing assurance of data quality and use of rigorous peer review as aspects of best available science). “Waters of the United States” Is a Legal Determination Informed by Science Jurisdiction under the CWA has both legal and scientific components. The CWA defines the term “navigable waters” as “waters of the United States,” which has been further refined by case law, regulation, and agency guidance (Congressional Research Service 2019). There is no question that traditional navigable waters, such as rivers, lakes, and the territorial seas (hereinafter collectively referred to as “primary waters”) are “waters of the United States.” There is also no question that the chemical, physical, and biological integrity of these primary waters are affected by activities upstream (e.g., Zhang et al. 2012). As Congress recognized, “[w]ater moves in hydrologic cycles, and it is essential that discharge of pollutants be controlled at the source” (U.S. Senate 1972). Scientific research plays a critical role in determining how upstream tributaries and waters adjacent to those tributaries affect the integrity of primary waters, and thus whether these upstream waters should qualify for CWA protection. As a Legal Matter, CWA Jurisdiction Requires a “Significant Nexus” to a Primary Water Interpreting the CWA, the U.S. Supreme Court has observed that the “regulation of activities that cause water pollution cannot rely on ... artificial lines ..., but must focus on all waters that together form the entire aquatic system” (United States v. Riverside Bayview Homes, Inc., 474 U.S. 121 (1985)). How far upstream from a traditional navigable water the EPA and the Corps may regulate has been controversial, in part because federalism concerns may be invoked (Owen 2017). Accordingly, while “waters of the United States” include more than primary waters, the CWA’s jurisdictional scope has limits. In Solid Waste Agency of Northern Cook County v. U.S. Army Corps of Engineers, the U.S. Supreme Court noted that the term “navigable” has some import in CWA jurisdictional determinations (531 U.S. 159 (2001)). As a result, agencies and courts have employed the “significant nexus” analysis endorsed by Justice Kennedy in Rapanos v. United States (547 U.S. 715 (2006) (Kennedy, J., concurring in the judgment)) to assess whether an upstream water has a sufficient chemical, physical, or biological connection to a traditional navigable water to warrant asserting CWA jurisdiction. This approach recognizes that upstream waters must be protected to ensure the integrity of primary waters (Rapanos v. United States, 547 U.S. 715 (2006)). As a Scientific Matter, the Clean Water Rule’s Approach to “Significant Nexus” Is Sound The Clean Water Rule relies on the best available science to establish criteria for the requisite “significant nexus” between primary waters and other waters. Primary waters do not exist in isolation (National Research Council 2001). Rather, they are heavily influenced by their interactions with streams, wetlands, and open waters within their watersheds. As the Connectivity Report correctly emphasizes: The structure and function of downstream waters highly depend on materials—broadly defined as any physical, chemical, or biological entity—that originate outside of the downstream waters. Most of the constituent materials in rivers, for example, originate from aquatic ecosystems located upstream in the drainage network or elsewhere in the drainage basin, and are transported to the river through flowpaths[.] (U.S. EPA Office of Research and Development 2015). The Clean Water Rule appropriately defines “significant nexus” using scientifically supported functions to demonstrate strong chemical, physical, and biological connections between upstream waters and primary waters. Since the Clean Water Rule was developed, a number of reviews have been published that provide overviews and updates on these connections and their importance (e.g., Cohen et al. 2016; Fritz et al. 2018; Lane et al. 2018). Although these recent studies were not part of the scientific record that formed the basis of the Clean Water Rule, they demonstrate that accumulating scientific evidence continues to substantiate the Clean Water Rule. Scientific literature strongly supports the nine functions listed in the Clean Water Rule’s “significant nexus” definition, each of which relates to the chemical, physical, and/or biological integrity of primary waters. Wetlands enhance the chemical integrity of downstream waters through trapping, transforming, and filtering pollutants (see Johnston et al. 1990). Wetlands also recycle nutrients and export organic material important for downstream food webs (see McClain et al. 2003; Smucker and Detenbeck 2014). For example, streams that flow intermittently are critical to certain life history stages of fish, including coho salmon (Larsen and Woelfle-Erskine 2018) as well as many invertebrates (Schofield et al. 2018). Microbially available organic matter in stream networks can be traced to seasonally connected wetland sources based on the molecular composition of its carbon (Hosen et al. 2018). Similarly, the functions of streams, wetlands, and open waters affect the physical integrity of downstream waters (see, e.g., Fletcher et al. 2014). These waters contribute flow to primary waters (see, e.g., Johnston and Shmagin 2008). Research has shown that many wetlands without a year-round surface connection to primary waters flow into perennial streams a significant amount of the time, thereby contributing water and other materials downstream (see, e.g., Golden et al. 2014; McDonough et al. 2015; Hosen et al. 2018; Epting et al. 2018; Evenson et al. 2018). For example, researchers used direct field measurements of connectivity to demonstrate that prairie pothole wetlands contribute significant amounts of water to receiving perennial streams through surface water connections (Brooks et al. 2018; Neff and Rosenberry 2018). Focusing on ten catchments across the United States, Thorslund et al. (2018) used chloride tracers to demonstrate that geographically isolated wetlands are hydrologically connected and integral elements in flow-generating networks. Recent advances in remote sensing have also allowed scientists to detect and quantify physical connections that provide temporally variable surface water flows between streams and wetlands that were previously considered isolated (Vanderhoof et al. 2016, 2017). Wetlands also retain and attenuate floodwaters, as well as store runoff (see Ogawa and Male 1986; Johnston 1993). Hydrological modeling recently showed that depressional wetlands in the Prairie Pothole Region attenuate peak flows, thus decreasing the probability of downstream flooding (Evenson et al. 2018). In addition, wetlands trap sediment and nutrients, thereby substantially reducing the degradation of downstream water quality (see Johnston et al. 1984). Extensive evidence demonstrates that wetlands act to remove nutrients, thereby regulating the movement of excess nitrogen and phosphorus to downstream waters (McClain et al. 2003; Jordan et al. 2011). As a recent study showed, at the catchment scale, geographically isolated wetlands can provide substantial water storage capacity that can optimize these wetland functions (Jones et al. 2018). Furthermore, research has confirmed that, like small streams in some regions (Alexander et al. 2000; Peterson et al. 2001), small wetlands play a disproportionately large role in landscape-scale nutrient processes (Cheng and Basu 2017). These are exactly the wetlands that are likely to be filled in and developed and thus are at greater risk without protection (Van Meter and Basu 2015). The Clean Water Rule’s definition of “significant nexus” also recognizes how streams, wetlands, and open waters affect the biological integrity of downstream waters. Such waters provide important foraging, nesting, breeding, spawning, and nursery habitat for species that occur in primary waters (see Semlitsch and Bodie 1998; Sheaves 2009; Pittman et al. 2014). Connectivity refers to “the degree to which components of a watershed are joined and interact by transport mechanisms that function across multiple spatial and temporal scales” (U.S. EPA Office of Research and Development 2015). Whether the functions of a particular stream, wetland, or open water (or a group of “similarly situated” waters) satisfy the legal threshold of “significant nexus” depends on the extent of its connectivity with primary waters. We examine the Clean Water Rule’s categorical application of the “significant nexus” test below. Best Available Science Supports the Clean Water Rule’s Categorical Treatment of Tributaries Scientific research demonstrates extensive connections between tributaries and their downstream primary waters sufficient to warrant categorical inclusion under the Clean Water Rule (see Turner and Rabalais 2003). The U.S. Supreme Court has held that federal agencies may craft a categorical rule to assert CWA jurisdiction over certain waters (United States v. Riverside Bayview Homes, Inc., 474 U.S. 121 (1985)). The Court noted that so long as “it is reasonable ... to conclude that, in the majority of cases” the category of waters has “significant effects on water quality and the aquatic ecosystem, its definition can stand” (United States v. Riverside Bayview Homes, Inc., 474 U.S. 121 (1985)). The Clean Water Rule’s Definition of Tributary Is Scientifically Sound The Clean Water Rule defines “tributary” in a manner consistent with scientific understanding. At its most basic level, a tributary is simply a waterbody that flows into a larger waterbody. From a scientific perspective, “a tributary is the smaller of two intersecting channels, and the larger is the main stem” (Benda et al. 2004). A standard stream ordering system classifies the smallest streams as first-order streams; when two streams meet, they form a second-order stream and so on (see Strahler 1957). The smaller waters are intrinsically linked to primary waters both structurally and functionally (see Whigham et al. 1988). Indeed, “[t]he great majority of the total length of river systems is comprised of lower-order or headwater systems” (Allan and Castillo 2007; see also Fritz et al. 2013). Under the Clean Water Rule, a “tributary ... contributes flow, either directly or through another water” to primary waters and is “characterized by the presence of the physical indicators of a bed and banks and an ordinary high water mark” (80 Federal Register 37,054). The Clean Water Rule notes that tributaries may be natural or human-made and include “rivers, streams, [and] canals,” as well as ditches that are not otherwise excluded by the Rule (80 Federal Register 37,054). From a scientific perspective, whether a tributary is natural or human-made is immaterial; what matters is whether the water contributes flow to another waterbody. Under the Clean Water Rule, a water meets the definition of a tributary even if it contributes flow to a primary water through a non-jurisdictional water. This approach is also sound because the scientific definition of tributary focuses on the hydrologic connection between waters. From a scientific perspective, the Clean Water Rule’s definition of “tributary” could be considered conservative. In addition to requiring a bed and banks (channels), it also provides that a tributary must have an ordinary high water mark (OHWM). In comments to the EPA, however, the Scientific Advisory Board noted that not all tributaries have OHWMs (U.S. EPA Scientific Advisory Board 2014). The OHWM requirement (which is ultimately a limitation on what constitutes a water of the United States) is not dictated by science, but we recognize that the agencies must set boundaries along gradients to apply the CWA on a national basis. Compelling Scientific Evidence Demonstrates that Tributaries Significantly Affect the Chemical, Physical, and Biological Integrity of Primary Waters The National Academy of Sciences has extensively documented the connections between tributaries and downstream waters (see, e.g., National Research Council 2000, 2011a, b). Scientific studies demonstrate how tributaries significantly affect the functions and integrity of downstream waters through chemical, physical, and biological interrelationships, especially regarding how physical aspects (e.g., flow) can influence chemical processes (e.g., pesticide contamination), which in turn can affect the biological features (e.g., species) of a water. Below we highlight a few examples of connections between tributaries and primary waters. Scientists find evidence of strong chemical connections between tributaries and downstream primary waters in the movement of contaminants and pathogens. Sediment-laden waters typically transport some contaminants (such as mercury) from tributaries to downstream waters (see Salomons and Förtsner 1984). Waterborne pathogens (such as bacteria and viruses) that originate from agricultural and municipal wastes are also transported to downstream waters through tributaries (see Jokinen et al. 2012; Pandey et al. 2014; Jalliffier-Verne et al. 2016). Pathogens may pose a risk to human health, highlighting the importance of regulating and protecting tributaries to ensure the integrity of primary waters. Tributaries also have important physical connections with downstream primary waters. The water flow from tributaries helps to create and maintain river networks. Indeed, most of the water in most rivers comes from tributaries (see, e.g., Alexander et al. 2007). Furthermore, tributaries support the metabolism of river ecosystems. For example, they export organic matter (dissolved and particulate) that is incorporated into the food webs of downstream waters (Hosen et al. 2018), and the resulting turbid water may shade and protect fish and amphibians from damage by ultraviolet radiation (e.g., Frost et al. 2006). Other biological connections relate to the passive and active transport of living organisms (see Meyer et al. 2007 (discussing how organisms rely on streams); Moreno-Mateos and Palmer 2016; Johnston 2017; Schofield et al. 2018). Accordingly, the Clean Water Rule’s categorical treatment of tributaries reflects scientific reality. Best Available Science Supports the Clean Water Rule’s Categorical Treatment of Adjacent Waters Based on Geographic Proximity Scientific research demonstrates that adjacent waters warrant regulation under the Clean Water Rule because of their chemical, physical, and biological connections to downstream primary waters. Compelling Scientific Evidence Demonstrates that Waters within 100 Ft of an OHWM Significantly Affect the Chemical, Physical, and Biological Integrity of Primary Waters Waters, including wetlands, ponds, oxbows, and impoundments, within 100 ft of an OHWM are “hotspots” of species diversity with important ecological functions that affect the flux of materials (water, sediment, energy, organic matter, pollutants, and organisms) to primary waters (see Groffman et al. 2003). These adjacent waters affect the movement of pollutants from uplands into streams and rivers; regulate stream temperatures, light, and flow regimes; reduce downstream flooding; and provide nursery areas and critical habitat for aquatic biota, including threatened and endangered species (see Ward et al. 2002). Riparian wetlands act as buffers, effectively reducing concentrations of nutrients and other pollutants. For example, riparian wetlands may remove up to 100% of the nitrate-nitrogen that enters them (see Fennessy and Cronk 1997). Nitrate is a serious water pollutant and a major contributor to coastal algal blooms, such as the Gulf of Mexico’s hypoxic “dead zone,” as well as nuisance algal blooms in many other surface waters (see Mitsch et al. 2005; see also Kosten et al. 2012). These adjacent waters can act as sources, sinks, or transformers of materials from upland habitats. As sources, adjacent waters contribute organic materials, such as leaf litter, that provide food (energy) for many in-stream species (see Vannote et al. 1980). They also carry woody debris, which increases habitat complexity and biodiversity (see Allan 1995; Ward et al. 2002). Adjacent waters are also major sinks for materials. By capturing and storing sediment eroded from nearby uplands, they reduce downstream sediment transport and its negative effects on fish feeding and spawning, macroinvertebrate communities, and overall habitat quality (see Newcombe and MacDonald 1991). These adjacent waters convert materials from one form to another; plants and algae can can take up nutrients and bind them in their tissues, reducing the risk of downstream eutrophication. Wetlands in particular mitigate nonpoint source pollution, such as insecticides and fertilizers, thus protecting stream water quality and drinking water supplies (e.g., Mitsch et al. 2005; Everich et al. 2011). Adjacent waters also slow the movement of materials and biota by providing temporary storage of excess water during times of high precipitation; this storage dissipates the energy of flows (reducing erosion and soil loss) and attenuates flood peaks (see Mitsch and Gosselink 2015). Hydrologic connections do not need to be continuous to have a substantial effect on downstream primary waters. Hydrologic connectivity involves longitudinal, lateral, and vertical exchange, and adjacent waters are intimately linked to streams and rivers both in space (i.e., proximity to the OHWM) and time (e.g., by means of high water and flood events). Seasonal high water levels increase connectivity, promoting the lateral movement of animals between lakes, wetlands, stream channels, and their adjacent waters. This movement facilitates use of critical spawning and nursery habitats by fish and supports the biological integrity of the system. Many fish are sustained by varied habitats dispersed throughout the watershed for spawning, nurseries, growth, and maturation (see Fausch et al. 2002). Overall, the benefits of protecting waters within 100 ft of an OHWM accrue both locally (at that point on the river system) and cumulatively (at the watershed scale). The Clean Water Rule’s categorical inclusion of these adjacent waters reflects scientific reality. Compelling Scientific Evidence Demonstrates that Waters within 100-Year Floodplains Significantly Affect the Chemical, Physical, and Biological Integrity of Primary Waters The Clean Water Rule’s coverage of waters within 100-year floodplains is based on scientific understanding of watershed dynamics. These dynamics include not only surface expressions of connectivity (floods), but also underlying hydrologic conditions. Every primary water has a watershed, which can be described as the land area that drains into that primary water and its tributaries (see Bierman and Montgomery 2014). During any flood event, primary waters and their tributaries may overflow their banks (Bierman and Montgomery 2014). The proportion of land that becomes obviously flooded (the “floodplain”) depends upon the rate and total amount of rainfall. The geographic extent of the floodplain also depends upon the watershed’s topography, soil saturation, and geological characteristics (see Osterkamp and Friedman 2000). A landscape with more topographic relief (steeper) will have a smaller floodplain than a flatter landscape where floodwaters more readily spread outward (see Howard 1996). Although every flood is unique in extent and duration, scientists describe floodplains statistically to characterize other hydrologic (non-flooding) features (see Pandey and Nguyen 1999). For example, the “100-year floodplain” represents the land area that has a 1% chance of being inundated by floodwaters in any given year (1/100 likelihood). This definition is entirely statistical; such floods can occur more often in a 100-year floodplain, even 2 years or more in a row. It is incorrect to conclude that waters on a 100-year floodplain have a connection with a primary water only once in a century because the hydrologic connections extend beyond surface flooding alone and into belowground material. Furthermore, changes in land use can affect flood dynamics. Increasing the proportion of the landscape that is covered with impermeable surfaces (such as streets and roofs) may increase flood intensity and duration (see Bedan and Clausen 2009). Floodwaters are only the surface expressions of a flood. Rainfall permeates into the soil and often moves underground toward open waterbodies, such as primary waters (see Alley et al. 2002; Malard et al. 2002). Groundwater movement also contributes to baseflow in the absence of a flood. This understanding results from tracer techniques that show large proportions of streamflow are derived from groundwater (e.g., Alley et al. 2002). Factors other than surface flooding determine the actual extent of hydrologic connections between waters in a floodplain. The direction of movement and the rate at which the water moves depend upon topography, geology, and rainfall (see Stanford and Ward 1993; Alley et al. 2002). Impermeable subsurface layers, like clay layers, can reduce the downward movement of water and force it to move laterally (see Bush and Johnston 1988). Often subsurface impermeable (or semi-permeable) layers are not level; they may slope toward waterbodies, and this subsurface lateral flow may re-emerge in a surface waterbody, such as a primary water. However, subsurface lateral flow can occur even without sloping impermeable layers; when more water pools in a particular subsurface location, lateral flow will occur from areas of higher pressure to areas of lower pressure, which may be river channels, wetlands, or lakes (Bear 2012). Many different types of waterbodies can occur in 100-year floodplains. Tributaries and other waters can be connected to a primary river in more than one way (see Amoros and Bornette 2002). Headwaters and tributaries may flow directly into primary waters, adding organic matter and constituents that create unique water chemistry in the primary water (see Gomi et al. 2002). Wetlands may border primary waters, buffering the input of floodwaters, altering the water chemistry of floodwaters and the primary water itself, and providing habitat and resources for local biota (see Zedler 2003). Even other waterbodies with no obvious surface connections to primary waters may still be hydrologically connected to them. Lakes, ponds, wetlands, and streams that flow into these apparently isolated waterbodies may have no surface connections to the primary water but, in addition to storing water as previously described, can have subsurface connections through groundwater (Bear 2012). These subsurface connections can carry water to primary waters; for example, water seeping down out of an apparently isolated waterbody may hit an impermeable layer and move laterally until it emerges in the primary waterbody (see Poole 2002). Therefore, loss of a superficially isolated waterbody can reduce water volume and alter flow characteristics of a primary water. Evidence for these connections can be observed in the physical and chemical properties of primary waters (see Malard et al. 2002). Temperature, alkalinity, salinity, nitrate, other chemicals and pollutants, and dyes have been used as tracers to show the impact of groundwater connections to surface waters (see Soulsby et al. 2007). Furthermore, additions of pollutants into apparently isolated waterbodies or disparate areas of the watershed can affect primary waters (see Lerner and Harris 2009). Tracer and stable isotope studies have established paths and rates of water movements, substantiating that a distant source can pollute primary waters (see Badruzzaman et al. 2012). These studies highlight the chemical, physical, and biological connections between a primary water and other waterbodies that are located within its 100-year floodplain, thus justifying the inclusion of these adjacent waters in the Clean Water Rule. Compelling Scientific Evidence Demonstrates that Waters within 1500 Ft of High Tide Lines of Tidally Influenced Primary Waters or OHWMs of the Great Lakes Significantly Affect the Integrity of these Primary Waters Scientific evidence strongly supports protecting waters located within 1500 ft of such primary waters. These waters have the same types of connections and functions as the tributaries and other adjacent waters discussed supra. Adjacent waters within 1500 ft of primary waters have important chemical connections to those waters. Adjacent waters that were thought to be isolated have become more saline, providing empirical data regarding the groundwater connection between adjacent waters and primary waters (see, e.g., Wood and Harrington 2014). In addition, adjacent waters in the 1500-ft zone may release freshwater into coastal waters, thereby reducing the salinity of these waters (see, e.g., Sklar and Browder 1998). Indeed, the inputs of groundwater into coastal waters are quite large, and groundwater can contain high levels of dissolved solids and nutrients (see, e.g., Moore 1996; Krest et al. 2000; Charette et al. 2001). As in inland systems, coastal wetlands remove nutrients, such as nitrate, thereby reducing down-gradient eutrophication in primary waters (see Ardón et al. 2013). Thus, adjacent waters protect and improve the quality of primary waters by removing harmful contaminants or transforming and transporting nutrients to primary waters (see Dahm et al. 2016). Adjacent waters also physically influence primary waters through surface and subsurface connections. Adjacent waters contribute flow to nearby primary waters and retain floodwaters and sediments (see, e.g., Barlow 2003). Further, adjacent waters have a significant impact on the biological integrity of primary waters. Wetlands near tidally influenced primary waters can serve as a critical source of freshwater for some species that use wetlands and coastal waters (see U.S. EPA and U.S. Department of the Army 2015). Adjacent wetlands, lakes, ponds, and other waters also provide important foraging and breeding habitat for coastal species and are an important refuge from predators (see, e.g., Jude and Pappas 1992; Sierszen et al. 2012a). Distance is but one factor that affects the connectivity between waters, and as with the other geographical distance limitations discussed supra, the agencies’ selection of 1500 ft as the distance limitation is conservative from a scientific perspective. Indeed, waters located beyond this threshold can be chemically, physically, and biologically connected to tidally influenced primary waters or the Great Lakes. While the categorical jurisdictional line could have been drawn farther from high tide lines, science supports connecting the majority of lakes, wetlands, ponds, and other waters located within this 1500-ft area to primary waters. Once again, the Clean Water Rule’s categorical inclusion of these adjacent waters reflects scientific reality. Conclusion The U.S. Supreme Court has held that federal agencies may protect waters on a categorical basis if most waters in that category have a significant effect on primary waters. The best available science overwhelmingly demonstrates that the waters treated categorically in the Clean Water Rule have significant chemical, physical, and biological connections to primary waters. Accordingly, we support the Clean Water Rule. Any effort to suspend or revise the Clean Water Rule must take into account this scientific record and explain how any proposed changes would contribute to furthering the goals of the Clean Water Act. Footnotes 1. The groups also argued that the EPA and the Corps, in promulgating the Clean Water Rule, violated the Administrative Procedure Act by acting “in excess of statutory jurisdiction, authority, or limitations, or short of statutory right,” 5 U.S.C. §706. Such arguments were based on the claim that the Clean Water Rule contravened the jurisdiction set forth in the Clean Water Act, the statute upon which the Clean Water Rule was grounded. These more legal—versus scientific—arguments are beyond the scope of this article. Notes Publisher’s Note Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations. References Abbott BW, Baranov V, Mendoza-Lera C, Nikolakopoulou M, Harjung A, Kolbe T, Balasubramanian MN, Vaessen TN, Ciocca F, Campeau A, Wallin MB, Romeijn P, Antonelli M, Gonçalves J, Datry T, Laverman AM, de Dreuzy JR, Hannah DM, Krause S, Oldham C, Pinay G (2016) Using multi-tracer inference to move beyond single-catchment ecohydrology. Earth-Science Reviews 160:19–42. CrossRefGoogle Scholar Administrative Procedure Act (2018) 5 U.S.C. §706Google Scholar Alexander RB, Smith RA, Schwarz GE (2000) Effect of stream channel size on the delivery of nitrogen to the Gulf of Mexico. Nature 403:758–761. CrossRefPubMedGoogle Scholar Alexander RB, Boyer EW, Smith RA, Schwarz GE, Moore RB (2007) The role of headwater streams in downstream water quality. Journal of the American Water Resources Association 43:41–59. CrossRefPubMedPubMedCentralGoogle Scholar Allan JD (1995) Stream ecology: structure and function of running waters, 1st edn. Chapman and Hall, New YorkCrossRefGoogle Scholar Allan JD, Castillo MM (2007) Stream ecology: structure and function of running waters, 2nd edn. Springer, The NetherlandsCrossRefGoogle Scholar Alley WA, Healy RW, LaBaugh J, Reilly TE (2002) Flow and storage in groundwater systems. Science 296:1985–1990. CrossRefPubMedGoogle Scholar Amoros C, Bornette G (2002) Connectivity and biocomplexity in waterbodies of riverine floodplains. Freshwater Biology 47:761–776. CrossRefGoogle Scholar Ardón M, Morse JL, Colman BP, Bernhardt ES (2013) Drought-induced saltwater incursion leads to increased wetland nitrogen export. Global Change Biology 19:2976–2985. CrossRefPubMedGoogle Scholar Badruzzaman M, Pinzon J, Oppenheimer J, Jacangelo JG (2012) Sources of nutrients impacting surface waters in Florida: a review. Journal of Environmental Management 109:80–92. CrossRefPubMedGoogle Scholar Barlow PM (2003) Ground water in freshwater-saltwater environments of the Atlantic coast. In: U.S. Geological Survey Circular 1262. U.S. Geological Survey. Available via Bear J (2012) Hydraulics of groundwater. Dover Publications, Inc., MineolaGoogle Scholar Bedan ES, Clausen JC (2009) Stormwater runoff quality and quantity from traditional and low impact development watersheds. Journal of the American Water Resources Association 4:998–1008. CrossRefGoogle Scholar Benda L et al (2004) The network dynamics hypothesis: how channel networks structure riverine habitats. BioScience 54:413–427.[0413:TNDHHC]2.0.CO;2Google Scholar Bertrand G et al (2014) Environmental tracers and indicators bringing together groundwater, surface water and groundwater-dependent ecosystems: importance of scale in choosing relevant tools. Environmental Earth Sciences 72:813–827. CrossRefGoogle Scholar Bierman PR, Montgomery DR (2014) Key concepts in geomorphology. W. H. Freeman and Company Publishers, New YorkGoogle Scholar Breyer SG et al (2011) Reference manual on scientific evidence, 3rd edn. Federal Judicial Center. Available via Brooks JR et al (2018) Estimating wetland connectivity to streams in the Prairie Pothole Region: an isotopic and remote sensing approach. Water Resources Research 54:955–977. CrossRefGoogle Scholar Bush PW, Johnston RH (1988) Ground-water hydraulics, regional flow, and ground-water development of the Floridan aquifer system in Florida and in parts of Georgia, South Carolina, and Alabama: regional aquifer-system analysis. In: U.S. Geological Survey Professional Paper 1403-C. U.S. Geological Survey. Available via Charette MA, Buesseler KO, Andrews JE (2001) Utility of radium isotopes for evaluating the input and transport of groundwater-derived nitrogen to a Cape Cod estuary. Limnology and Oceanography 46:465–470. CrossRefGoogle Scholar Cheng FY, Basu NB (2017) Biogeochemical hotspots: role of small water bodies in landscape nutrient processing. Water Resources Research 53:5038–5056. CrossRefGoogle Scholar Clean Water Act (2018) 33 U.S.C. §1251 et seqGoogle Scholar Cohen MJ et al (2016) Do geographically isolated wetlands influence landscape functions? Proceedings of the National Academy of Sciences of the United States of America 113:1978–1986. CrossRefPubMedPubMedCentralGoogle Scholar Congressional Research Service (2019) Evolution of the meaning of “waters of the United States” in the clean water act. Available via Dahm CN et al (2016) Nutrient dynamics of the Delta: effects on primary producers. San Francisco Estuary & Watershed Science 14:4 Art. 4. CrossRefGoogle Scholar DeLaune RD et al (2013) Methods in biogeochemistry of wetlands. Soil Science Society of America, Inc., MadisonGoogle Scholar Epting SM et al (2018) Landscape metrics as predictors of hydrologic connectivity between coastal plain forested wetlands and streams. Hydrological Processes 32:516–532. CrossRefPubMedPubMedCentralGoogle Scholar Evenson GR et al (2018) Depressional wetlands affect watershed hydrological, biogeochemical, and ecological functions. Ecological Applications 28:953–966. CrossRefPubMedGoogle Scholar Everich R et al. (2011) Efficacy of a vegetative buffer for reducing the potential runoff of the insect growth regulator novaluron. In: Goh KS et al. (eds) Pesticide mitigation strategies for surface water quality pp 175–188. Fausch KD et al (2002) Landscapes to riverscapes: bridging the gap between research and conservation of stream fishes. BioScience 52:483–498.[0483:LTRBTG]2.0.CO;2Google Scholar Fennessy MS, Cronk J (1997) The effectiveness and restoration potential of riparian ecotones for the management of nonpoint source pollution, particularly nitrate. Critical Reviews in Environmental Science and Technology 27:285–317. CrossRefGoogle Scholar Fletcher TD, Vietz G, Walsh CJ (2014) Protection of stream ecosystems from urban stormwater runoff: the multiple benefits of an ecohydrological approach. Progress in Physical Geography 38:543–555. CrossRefGoogle Scholar Fritz KM, Hagenbuch E, D'Amico E, Reif M, Wigington PJ Jr, Leibowitz SG, Comeleo RL, Ebersole JL, Nadeau TL (2013) Comparing the extent and permanence of headwater streams from two field surveys to values from hydrographic databases and maps. Journal of the American Water Resources Association 49:867–882. CrossRefGoogle Scholar Fritz KM et al (2018) Physical and chemical connectivity of streams and riparian wetlands to downstream waters: a synthesis. Journal of the American Water Resources Association 54:323–345. CrossRefPubMedPubMedCentralGoogle Scholar Frost PC, Mack A, Larson JH, Bridgham SD, Lamberti GA (2006) Environmental controls of UV-B radiation in forested streams of northern Michigan. Photochemistry and Photobiology 82:781–786. CrossRefPubMedGoogle Scholar Gardner RC (2011) Lawyers, swamps, and money: U.S. wetland law, policy, and politics. Island Press, Washington, DCCrossRefGoogle Scholar Gardner RC, Finlayson CM (2018) Global wetland outlook: state of the World’s wetlands and their services to people. Ramsar Secretariat, GlandGoogle Scholar Gardner RC, Okuno E (2018) The shifting boundaries of clean water act jurisdiction. Wetland Science & Practice 35:317–323Google Scholar Golden HE, Lane CR, Amatya DM, Bandilla KW, Raanan Kiperwas H, Knightes CD, Ssegane H (2014) Hydrologic connectivity between geographically isolated wetlands and surface water systems: a review of select modeling methods. Environmental Modelling and Software 53:190–206. CrossRefGoogle Scholar Gomi T et al (2002) Understanding processes and downstream linkages of headwater systems: headwaters differ from downstream reaches by their close coupling to hillslope processes, more temporal and spatial variation, and their need for different means of protection from land use. BioScience 52:905–916.[0905:UPADLO]2.0.CO;2Google Scholar Goodstein D (2011) How science works. In: Federal judicial center reference manual on scientific evidence, 3rd edn, p 37Google Scholar Gray MJ et al (2013) Management of wetlands for wildlife. In: Anderson JT, Davis CA (eds) Wetland techniques, Applications and management, vol 3. Springer, Dordrecht, pp 121–180. CrossRefGoogle Scholar Groffman PM, Bain DJ, Band LE, Belt KT, Brush GS, Grove JM, Pouyat RV, Yesilonis IC, Zipperer WC (2003) Down by the riverside: urban riparian ecology. Frontiers in Ecology and the Environment 1:315–321.[0315:DBTRUR]2.0.CO;2Google Scholar Haack S (2003) Defending science—within reason: between scientism and cynicism. Prometheus Books, Amherst, New YorkGoogle Scholar Hancock PJ, Hunt RJ, Boulton AJ (2009) Preface: hydrogeoecology, the interdisciplinary study of groundwater dependent ecosystems. Hydrogeology Journal 17:1–3. CrossRefGoogle Scholar Hey DL, Philippi NS (2006) Flood reduction through wetland restoration: the upper Mississippi River basin as a case history. Restoration Ecology 3:4–17. CrossRefGoogle Scholar Hosen JD et al (2018) Dissolved organic matter variations in coastal plain wetland watersheds: the integrated role of hydrological connectivity, land use, and seasonality. Hydrological Processes 32:1664–1681. CrossRefGoogle Scholar Howard AD (1996) Modelling channel evolution and floodplain morphology. In: Anderson MG et al (eds) Floodplain processes. Wiley, New York, pp 15–62Google Scholar Jalliffier-Verne I, Heniche M, Madoux-Humery AS, Galarneau M, Servais P, Prévost M, Dorner S (2016) Cumulative effects of fecal contamination from combined sewer overflows: management for source water protection. Journal of Environmental Management 174:62–70. CrossRefPubMedGoogle Scholar Johnston CA (1991) Sediment and nutrient retention by freshwater wetlands: effects on surface water quality. Critical Reviews in Environmental Control 21:491–565. CrossRefGoogle Scholar Johnston CA (1993) Material fluxes across wetland ecotones in northern landscapes. Ecological Applications 3:424–440. CrossRefPubMedGoogle Scholar Johnston CA (2017) Beavers: boreal ecosystem engineers. Springer, Switzerland. CrossRefGoogle Scholar Johnston CA, Shmagin BA (2008) Regionalization, seasonality, and trends of streamflow in the U.S. Great Lakes Basin. Journal of Hydrology 362:69–88. CrossRefGoogle Scholar Johnston CA, Bubenzer GD, Lee GB, Madison FW, Mc Henry JR (1984) Nutrient trapping by sediment deposition in a seasonally flooded lakeside wetland. Journal of Environmental Quality 13:283–290. CrossRefGoogle Scholar Johnston CA, Detenbeck NE, Niemi GJ (1990) The cumulative effect of wetlands on stream water quality and quantity: a landscape approach. Biogeochemistry 10:105–141. CrossRefGoogle Scholar Jokinen CC, Edge TA, Koning W, Laing CR, Lapen DR, Miller J, Mutschall S, Scott A, Taboada EN, Thomas JE, Topp E, Wilkes G, Gannon VPJ (2012) Spatial and temporal drivers of zoonotic pathogen contamination of an agricultural watershed. Journal of Environmental Quality 41:242–252. CrossRefPubMedGoogle Scholar Jones CN, Evenson GR, McLaughlin DL, Vanderhoof MK, Lang MW, McCarty GW, Golden HE, Lane CR, Alexander LC (2018) Estimating restorable wetland water storage at landscape scales. Hydrological Processes 32:305–313. CrossRefPubMedPubMedCentralGoogle Scholar Jordan SJ, Stoffer J, Nestlerode JA (2011) Wetlands as sinks for reactive nitrogen at continental and global scales: a meta-analysis. Ecosystems 14:144–155. CrossRefGoogle Scholar Jude DJ, Pappas J (1992) Fish utilization of Great Lakes coastal wetlands. Journal of Great Lakes Research 18:651–672. CrossRefGoogle Scholar Kondolf GM, Piégay H (eds) (2016) Tools in fluvial geomorphology, 2nd edn. New York, WileyGoogle Scholar Kosten S, Huszar VLM, Bécares E, Costa LS, Donk E, Hansson LA, Jeppesen E, Kruk C, Lacerot G, Mazzeo N, Meester L, Moss B, Lürling M, Nõges T, Romo S, Scheffer M (2012) Warmer climates boost cyanobacterial dominance in shallow lakes. Global Change Biology 18:118–126. CrossRefGoogle Scholar Krest JM, Moore WS, Gardner LR, Morris JT (2000) Marsh nutrient export supplied by groundwater discharge: evidence from radium measurements. Global Biogeochemical Cycles 14:167–176. CrossRefGoogle Scholar Lane CR et al (2018) Hydrological, physical, and chemical functions and connectivity of non-floodplain wetlands to downstream waters: a review. Journal of the American Water Resources Association 54:346–371. CrossRefGoogle Scholar Larsen LG, Woelfle-Erskine C (2018) Groundwater is key to salmonid persistence and recruitment in intermittent Mediterranean-climate streams. Water Resources Research 54:8909–8930. CrossRefGoogle Scholar Layzer JA (2008) Natural experiments: ecosystem-based management and the environment. MIT Press, CambridgeCrossRefGoogle Scholar Leibowitz SG et al (2018) Connectivity of streams and wetlands to downstream waters: an integrated systems framework. Journal of the American Water Resources Association 54:298–322. CrossRefPubMedPubMedCentralGoogle Scholar Lerner DN, Harris B (2009) The relationship between land use and groundwater resources and quality. Land Use Policy 26:S265–S273. CrossRefGoogle Scholar Malard F et al (2002) A landscape perspective of surface-subsurface hydrological exchanges in river corridors. Freshwater Biology 47:621–640. CrossRefGoogle Scholar Martínez-Carreras N, Wetzel CE, Frentress J, Ector L, McDonnell JJ, Hoffmann L, Pfister L (2015) Hydrological connectivity as indicated by transport of diatoms through the riparian–stream system. Hydrology and Earth System Sciences Discussions 12:2391–2434. CrossRefGoogle Scholar McClain ME et al (2003) Biogeochemical hot spots and hot moments at the interface of terrestrial and aquatic ecosystems. Ecosystems 6:301–312. CrossRefGoogle Scholar McDonough OT et al (2015) Surface hydrologic connectivity between Delmarva Bay wetlands and nearby streams along a gradient of agricultural alteration. Wetlands 35:41–53. CrossRefGoogle Scholar Meyer JL, Strayer DL, Wallace JB, Eggert SL, Helfman GS, Leonard NE (2007) The contribution of headwater streams to biodiversity in river networks. Journal of the American Water Resources Association 43:86–103. CrossRefGoogle Scholar Mitsch WJ, Gosselink J (2015) Wetlands, 5th edn. Wiley, New YorkGoogle Scholar Mitsch WJ, Day JW, Zhang L, Lane RR (2005) Nitrate-nitrogen retention in the Mississippi River basin. Ecological Engineering 24:267–278. CrossRefGoogle Scholar Moore WS (1996) Large groundwater inputs to coastal waters revealed by 226Ra enrichments. Nature 380:612–614. CrossRefGoogle Scholar Moreno-Mateos D, Palmer MA (2016) Watershed processes as drivers for aquatic ecosystem restoration. In: Palmer MA et al (eds) Foundations of restoration ecology, 2nd edn. Island Press, Washington, DC. CrossRefGoogle Scholar Mulholland PJ et al (1990) Measurement of phosphorus uptake length in streams: comparison of radiotracer and stable PO4 releases. Canadian Journal of Fisheries and Aquatic Sciences 47:2351–2357. CrossRefGoogle Scholar National Judicial College (2010) Hydrologic modeling benchbook. Available via National Research Council (1995) Wetlands: characteristics and boundaries. National Academy Press, Washington, DC. CrossRefGoogle Scholar National Research Council (2000) Watershed management for potable water supply: assessing the New York City strategy. The National Academies Press, Washington, DC. CrossRefGoogle Scholar National Research Council (2001) Compensating for wetland losses under the clean water act. National Academy Press, Washington, DC, pp 46–59Google Scholar National Research Council (2011a) Missouri river planning: recognizing and incorporating sediment management. National Academy Press, Washington, DC. CrossRefGoogle Scholar National Research Council (2011b) Achieving nutrient and sediment reduction goals in the Chesapeake Bay: an evaluation of program strategies and implementation. The National Academy Press, Washington, DC. CrossRefGoogle Scholar Neff BP, Rosenberry DO (2018) Groundwater connectivity of upland-embedded wetlands in the prairie pothole region. Wetlands 38:51–63. CrossRefGoogle Scholar Newcombe CP, MacDonald DD (1991) Effects of suspended sediments on aquatic ecosystems. North American Journal of Fisheries Management 11:72–82.<0072:EOSSOA>2.3.CO;2 CrossRefGoogle Scholar Ogawa H, Male JW (1986) Simulating the flood mitigation role of wetlands. Journal of Water Resources Planning and Management 112:114–128. CrossRefGoogle Scholar Osterkamp WR, Friedman JM (2000) The disparity between extreme rainfall events and rare floods—with emphasis on the semi-arid American west. Hydrological Processes 14:2817–2829.<2817::AID-HYP121>3.0.CO;2-B CrossRefGoogle Scholar Owen D (2017) Little streams and legal transformations. Utah Law Review 2017:1–55 Available via Google Scholar Pandey GR, Nguyen V-T-V (1999) A comparative study of regression based methods in regional flood frequency analysis. Journal of Hydrology 225:92–101. CrossRefGoogle Scholar Pandey PK, Kass PH, Soupir ML, Biswas S, Singh VP (2014) Contamination of water resources by pathogenic bacteria. AMB Express 4:51. CrossRefPubMedPubMedCentralGoogle Scholar Pendleton LH (ed) (2008) The economic and market value of coasts and estuaries: what’s at stake? Restore America’s Estuaries, Arlington, VA. Available via Peterson BJ, Wollheim WM, Mulholland PJ, Webster JR, Meyer JL, Tank JL, Marti E, Bowden WB, Valett HM, Hershey AE, McDowell W, Dodds WK, Hamilton SK, Gregory S, Morrall DD (2001) Control of nitrogen export from watersheds by headwater streams. Science 292:86–90. CrossRefPubMedGoogle Scholar Pittman SE, Osbourn MS, Semlitsch RD (2014) Movement ecology of amphibians: a missing component to understanding amphibian declines. Biological Conservation 169:44–53. CrossRefGoogle Scholar Poole GC (2002) Fluvial landscape ecology: addressing uniqueness within the river discontinuum. Freshwater Biology 41:641–660. CrossRefGoogle Scholar Rinderer M et al (2018) Assessing structural, functional and effective hydrologic connectivity with brain neuroscience methods: state-of-the-art and research directions. Earth-Science Reviews 178:29–47. CrossRefGoogle Scholar Salomons W, Förtsner U (1984) Metals in the hydrocycle. Springer-Verlag, BerlinCrossRefGoogle Scholar Sarukhán et al (eds) (2005) Millennium ecosystem assessment: ecosystems and human well-being: wetlands and water. World Resources Institute, Washington, DCGoogle Scholar Schofield KA, Alexander LC, Ridley CE, Vanderhoof MK, Fritz KM, Autrey BC, DeMeester JE, Kepner WG, Lane CR, Leibowitz SG, Pollard AI (2018) Biota connect aquatic habitats throughout freshwater ecosystem mosaics. Journal of the American Water Resources Association 54:372–399. CrossRefGoogle Scholar Semlitsch RD, Bodie JR (1998) Are small, isolated wetlands expendable? Conservation Biology 12:1129–1133. CrossRefGoogle Scholar Sheaves M (2009) Consequences of ecological connectivity: the coastal ecosystem mosaic. Marine Ecology Progress Series 391:107–115. CrossRefGoogle Scholar Sierszen ME, Morrice JA, Trebitz AS, Hoffman JC (2012a) A review of selected ecosystem services provided by coastal wetlands of the Laurentian Great Lakes. Aquatic Ecosystem Health and Management 15:92–106. CrossRefGoogle Scholar Sierszen ME, Brazner JC, Cotter AM, Morrice JA, Peterson GS, Trebitz AS (2012b) Watershed and lake influences on the energetic base of coastal wetland food webs across the Great Lakes basin. Journal of Great Lakes Research 38:418–428. CrossRefGoogle Scholar Sklar FH, Browder JA (1998) Coastal environmental impacts brought about by alterations to freshwater flow in the Gulf of Mexico. Environmental Management 22:547–562. CrossRefPubMedGoogle Scholar Smucker NJ, Detenbeck NE (2014) Meta-analysis of lost ecosystem attributes in urban streams and the effectiveness of out-of-channel management practices. Restoration Ecology 22:741–748. CrossRefGoogle Scholar Soulsby C, Tetzlaff D, van den Bedem N, Malcolm IA, Bacon PJ, Youngson AF (2007) Inferring groundwater influences on surface water in montane catchments from hydrochemical surveys of springs and streamwaters. Journal of Hydrology 333:199–213. CrossRefGoogle Scholar Stanford JA, Ward JV (1993) An ecosystem perspective of alluvial rivers: connectivity and the hyporheic corridor. Journal of the North American Benthological Society 12:48–60. CrossRefGoogle Scholar Strahler AN (1957) Quantitative analysis of watershed geomorphology. Transactions of the American Geophysical Union 38:913–920. CrossRefGoogle Scholar Sullivan PJ et al (2006) Defining and implementing best available science for fisheries and environmental science, policy, and management. Fisheries 31:460 Available via Google Scholar Thorslund J, Cohen MJ, Jawitz JW, Destouni G, Creed IF, Rains MC, Badiou P, Jarsjö J (2018) Solute evidence for hydrological connectivity of geographically isolated wetlands. Land Degradation & Development 29:3954–3962. CrossRefGoogle Scholar Turner RE, Rabalais NN (2003) Linking landscape and water quality in the Mississippi River basin for 200 years. BioScience 53:563–572.[0563:LLAWQI]2.0.CO;2Google Scholar U.S. Army Corps of Engineers and U.S. EPA (2015) Clean Water Rule: Definition of “Waters of the United States.” 80 Federal Register 37,054Google Scholar U.S. Army Corps of Engineers and U.S. EPA (2018a) Definition of “Waters of the United States”—Addition of an Applicability Date to 2015 Clean Water Rule. 83 Federal Register 5200Google Scholar U.S. Army Corps of Engineers and U.S. EPA (2018b) Proposed rule: revised definition of “waters of the United States” (pre-publication version). Available via U.S. EPA and U.S. Department of the Army (2015) Technical support document for the clean water rule: definition of waters of the United States. Available via U.S. EPA Office of Research & Development (2015) Connectivity of streams and wetlands to downstream waters: a review and synthesis of the scientific evidence. Available via U.S. EPA Scientific Advisory Board (2014) Science Advisory Board (SAB) consideration of the adequacy of the scientific and technical basis of the EPA’s proposed rule titled “Definition of Waters of the United States under the Clean Water Act.” Letter to Gina McCarthy, EPA Administrator. Available via U.S. Senate (1972) Report 92–414Google Scholar U.S. Supreme Court (1983) Motor Vehicle Mfrs. Ass’n v. State Farm Mut. Auto. Ins. Co., 463 U.S. 29Google Scholar U.S. Supreme Court (1985) United States v. Riverside Bayview Homes, Inc., 474 U.S. 121Google Scholar U.S. Supreme Court (2001) Solid Waste Agency of North Cook County v. U.S. Army Corps of Engineers, 531 U.S. 159Google Scholar U.S. Supreme Court (2006) Rapanos v. United States, 547 U.S. 715Google Scholar Van Meter KJ, Basu NB (2015) Signatures of human impact: size distributions and spatial organization of wetlands in the prairie pothole landscape. Ecological Applications 25:451–465. CrossRefPubMedGoogle Scholar Vanderhoof MK et al (2016) Temporal and spatial patterns of wetland extent influence variability of surface water connectivity in the Prairie Pothole Region, United States. Landscape Ecology 31:805–824. CrossRefGoogle Scholar Vanderhoof MK et al (2017) Patterns and drivers for wetland connections in the Prairie Pothole Region, United States. Wetlands Ecology and Management 25:275–297. CrossRefGoogle Scholar Vannote RL, Minshall GW, Cummins KW, Sedell JR, Cushing CE (1980) The river continuum concept. Canadian Journal of Fisheries and Aquatic Sciences 37:130–137. CrossRefGoogle Scholar Ward JV et al (2002) Riverine landscape diversity. Freshwater Biology 47:517–539. CrossRefGoogle Scholar Whigham DF, Chitterling C, Palmer B (1988) Impacts of freshwater wetlands on water quality: a landscape perspective. Environmental Management 12:663–671. CrossRefGoogle Scholar Wood C, Harrington GA (2014) Influence of seasonal variations in sea level on the salinity regime of a coastal groundwater-fed wetland. Groundwater 53:90–98. CrossRefGoogle Scholar Wu K, Johnston CA (2008) Hydrologic comparison between a forested and a wetland/lake dominated watershed using SWAT. Hydrological Processes 22:1431–1442. CrossRefGoogle Scholar Zedler JB (2003) Wetlands at your service: reducing impacts of agriculture at the watershed scale. Frontiers in Ecology and the Environment 1:65–72.[0065:WAYSRI]2.0.CO;2Google Scholar Zhang T et al (2012) Evaluating the effects of upstream lakes and wetlands on lake phosphorus concentrations using a spatially-explicit model. Landscape Ecology 27:1015–1030. CrossRefGoogle Scholar Copyright information © The Author(s) 2019 Open Access This article is distributed under the terms of the Creative Commons Attribution 4.0 International License (, which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made. Authors and Affiliations Royal C. Gardner1Email authorView author's OrcID profileErin Okuno1Steph Tai2M. Siobhan Fennessy3Carol A. Johnston4Marinus L. Otte5Margaret Palmer6James E. Perry7Charles Simenstad8Benjamin R. Tanner9Dan Tufford10R. Eugene Turner11Kirsten Work9Scott C. Yaich12Joy B. Zedler21.Stetson UniversityGulfportUSA2.University of WisconsinMadisonUSA3.Kenyon CollegeGambierUSA4.South Dakota State UniversityBrookingsUSA5.North Dakota State UniversityFargoUSA6.University of MarylandCollege ParkUSA7.College of William and MaryWilliamsburgUSA8.University of WashingtonSeattleUSA9.Stetson UniversityDeLandUSA10.University of South CarolinaColumbiaUSA11.Louisiana State UniversityBaton RougeUSA12.Ducks UnlimitedMemphisUSA

This is a preview of a remote PDF:

Royal C. Gardner, Erin Okuno, Steph Tai, M. Siobhan Fennessy, Carol A. Johnston, Marinus L. Otte, Margaret Palmer, James E. Perry, Charles Simenstad, Benjamin R. Tanner, Dan Tufford, R. Eugene Turner, Kirsten Work, Scott C. Yaich, Joy B. Zedler. Advocating for Science: Amici Curiae Brief of Wetland and Water Scientists in Support of the Clean Water Rule, Wetlands, 2019, 1-12, DOI: 10.1007/s13157-019-01160-z