Rio+Grande+Group+Project

By: Ryan, Lexi, Justin, Lyle, Valerie and Harris


 * Introduction and Background **

The Rio Grande watershed is the fifth largest in North America at 355,500 mi2 and is approximately 2000 mi long, extending from the San Juan Mountains sometimes reaching the Gulf of Mexico, as shown in Figs. 1 and 2. The Rio Grande flows through 7structural basins (San Luis, Espanola, Santo Domingo, Albuquerque, Socorro, La Jencia, and San Marcial) known together as the Rio Grande Rift. The Albuquerque Basin is further subdivided into three structural sub-basins; Santo Domingo (not the same as before), Calabacillas, and Belen (MRGESCP, 2004). These are structural or geologic basins; however, the Middle Rio Grande Basin of this paper is a geologic basin defined by Cenozoic age deposits found along the Rio Grande from approximately Cochiti Dam to San Acacia that does not necessarily correspond to the previously mentioned structural units. The MRG Basin’s geology is mostly basin fill sediments, known as the Santa Fe Group that has been deposited by the Rio Grande over the past 30 million years (MRGESCP, 2004) and is up to thousands of feet thick in some places (Bartolino & Cole, 2002). Santa Fe Group sediments are unconsolidated to moderately consolidated sand, gravel, silt and clay (Bexfield, 2010).



The Middle Rio Grande Basin Valley, a sub-basin of the Rio Grande watershed, extends from Cochiti Lake downstream to San Acacia. It covers approximately 3,060 square miles in central New Mexico. The counties wit hin that area are Santa Fe, Sandoval, Bernalillo, Valencia, Socorro, Torrance, and Cibola (USGS, 2012). The Rio Grande in this area flows into a broad basin valley, shown in Fig. 2. Also shown in Fig. 2 is the land use, mostly urban with some agriculture centered along the river. As of 2000 the MRG Basin's population was approximately 690,000 (USGS, 2012), almost half of the states population.


 * Cochiti Dam **

Cochiti Dam was completed November 1973 to provide flood control and sediment retention. Cochiti Dam controls a drainage area of about 37,800 km2 (Richard & Julien, 2003). Construction of the dam has resulted in significant impacts downstream including degradation of the channel bed and coarsening of the bed from sand to gravel size (Richard & Julien, 2003). Decreased spring peak flows and the incision of the bed of the Rio Grande following construction of Cochiti Dam has resulted in a river channel that is detached from its floodplain. Cottonwood forests are now competing with exotic species such as Russian Olive, Siberian Elm, and Asian Saltcedar or tamarisk.


 * Fish Communities of the Rio Grande **

In most arid rivers of North America the fish assemblages have been affected by anthropogenic disturbances such as loss of habitat, water development and the introduction of non-native species (Bestgen and Platania 1991). The native fish fauna of the Rio Grande is in decline and the modern fauna include many introduced taxa (Platania 1991). The native fish community of Rio Grande within New Mexico is thought to consist of 16-27 species (Platania 1991). With the Albuquerque basin (Sandoval, Bernalillo, Valencia, and Socorro counties, NM) (Hoagstrom et al. 2010) identified 22 native fish species and 22 species that are either non-native to their study area or non-native to the entire Rio Grande drainage.

Fluvial fishes of the Albuquerque and Belen valleys are thought to have been extirpated in two periods (Hoagstrom et al. 2010). The first extirpation period, pre-1915, when Elephant Butte Dam was finalized, resulted in the disappearance of large-bodied, big-river natives (shovelnose sturgeon Scaphirhynchus platorynchus, [|longnose gar] Lepisosteus osseus, [|American eel]Anguilla rostrata, blue sucker Cycleptus elongatus, [|smallmouth buffalo]Ictiobus bubalus, gray redhorse Moxostoma congestum, blue catfish Ictalurus furcatus, [|flathead catfish] Pylodictis olivaris, [|freshwater drum]Aplodinotus grunniens). The historical presences of catadromous American eels within the Albuquerque valley indicate a continuous migration to the gulf of Mexico (Koster, 1957).

The second extirpation period, post-1915, resulted in disappearance of native fluvial minnows ([|Rio Grande speckled chub]Macrhybopsis aestivalis, [|Rio Grande shiner]Notropis jemezanus, [|phantom shiner]Notropis orca, Rio Grande bluntnose shiner Notropis simus) that persisted long enough to be documented by historical surveys of the mid-20th century (Hoagstrom et al. 2010). The first extirpation was due to the increasing aridity and dewatering. The second extirpation of fluvial minnows (cyprinidae) has been thought to be caused by additional dams, river manipulation, urbanization, increased water withdrawals, and invasion of non-native aquatic organisms (Bestgen and Platania 1991).

The Rio Grande silvery minnow (Hybognathus amarus) is the only remaining member of the reproductive guild of cyprinids that spawn eggs that are naturally buoyant (U.S. Fish and Wildlife Service 2010). The species was found in the Rio Grande from Espanola, New Mexico to the gulf of Mexico (Bestgen and Platania 1991), the Pecos River from Santa Rosa to the confluence with the Rio Grande (Pfieger 1980), and in the lower Jemez River and This species was once the most widespread and abundant species in the Rio Grande basin of New Mexico, Texas and Mexico (Bestgen and Platania 1991). Currently, Rio Grandesilvery minnow occupies seven percent of its former range, and is fragmented by diversion dams (U.S. Fish and Wildlife Service 2010). A non-essential experimental populationwas reintroduced into the Big Bend reach of the Rio Grande in Texas, within [|Big Bend National Park], to establish an additional self-sustaining population of H. amarus (U.S. Fish and Wildlife Service 2010).
 * [|Rio Grande Silvery Minnow] **

H. amarus was declared an endangered species under the Endangered Species Act in 1994. [|Critical habitat]was designated by the Service in 2003, to include the Rio Grande downstream of Cochiti reservoir to north of Elephant Butte reservoir (252 kilometers). The lateral extent of critical habitat is defined by area that is bound by existing levees, or 91.4 meters of riparian zone adjacent to each side of the bank full stage of the middle Rio Grande (U.S. Fish and Wildlife Service 2010). Specific water management and restoration actions are required to meet the [|Biological Opinion] written by the Service in 2003. Requirements include: Salvage of the species during river intermittency, reintroduction, interagency coordination of daily river and reservoir operations, improvements to irrigation metering and management, indirect use of native Rio Grande water, release of stored San Juan-Chama Project water, and pumping from the Low Flow Conveyance Channel to the river.

The [|Recovery Plan](U.S. Fish and Wildlife Service 2010) also requires a strategic program to assist agencies when determining where to initiate habitat construction essential to preventing population decline or extinction. Habitat modifications should occur within occupied reaches and reintroduction areas and create flooded surfaces during the spawning period of H. amarus (U.S. Fish and Wildlife Service 2010). Hydrological and fish monitoring occurs at multiple restored and unrestored sites under similar environmental conditions to determine the effectiveness of restoration activities of H. amarus populations dynamics.

** The Southwestern Willow Flycatcher **
The Southwestern Willow Flycatcher (flycatcher) was listed as federally endangered in 1995. The final [|recovery plan]was issued in 2002. The flycatcher is found in the U.S. from May until September. It winters in southern Mexico, Central America, and northern South America (Unitt, 1987). In New Mexico, the Southwestern Willow Flycatcher is distributed in nine drainages (Gila, Rio Grande, Rio Chama, Coyote Creek, Nutria Creek, Rio Grande de Ranchos, Zuni, Bluewater Creek, and San Francisco). The flycatcher is an endangered species on the U.S. Fish and Wildlife Service Endangered Species List and critical habitat has been designated in the MRG, though not in the Proposed Action Area. As of 1996, it was estimated that there were only about 400 Southwestern Willow Flycatchers in New Mexico, representing about 42% of the total population of the subspecies. Southwestern Willow Flycatchers occur in riparian habitats along rivers, streams, or other wetlands, where dense growth of willows (//Salix //spp.), seepwillow, arrow weed (//Pluchea //sp.), saltcedar or other plants are present, often with a scattered overstory of cottonwood (Unitt 1987; Sogge et al//. //, 1997; Finch and Stoleson, 2000). These riparian communities provide nesting and foraging habitat. Throughout the range of Southwestern Willow Flycatcher, these riparian habitats tend to be rare, widely separated, small and often linear locales, separated by vast expanses of arid lands. The Southwestern Willow Flycatcher is endangered by extensive loss and modification of suitable riparian habitat and other factors, including brood parasitism by the Brown-Headed Cowbird.

[|The Middle Rio Grande Endangered Species Collaborative Program (MRGESCP)]
==== The Middle Rio Grande Endangered Species Collaborative Program (MRGESCP) is partnership of federal, state, tribal and local government and non-governmental entities. Court ordered mediation lead to the formation of the MRGESCP. As of July 2009, 17 signatories to protect and improve the status of endangered species associated with the MRG. The MRGESCP includes various workgroups and committees (Executive Committee, Program Management, Habitat Restoration, Public Information Outreach, Science, Species Water Management, Hydrology and HOC, and Population Viability Analysis) The MRGESCP follows the Biological Opinion issued in 2003. The current BO expires in 2013. In 2012 the [|Corps] and [|BOR] (links to BA is the hyperlink) have reinitiated consultation with the USFWS and published biological assessments. The [|goals] of the MRGESCP are to: ====

4. Report to the community at large about the work of the Collaborative Program.
Congress provided approximately $115.8 million to Reclamation from FY2001 to 2009 with an approximate non-federal match of $12.7 million to support Program activities. Reclamation serves the leadership role for the Program. Accomplishments include acquisition of over 158,290 acre-feet of supplemental water from willing lessors from FY2003-2009. The Corps has received additional funding from congress to support Program activities.

The flood pulse is the key driving force for the existence, productivity and interactions of the major biota in river-floodplain systems (Junk et al. 1989). Flood pulses in natural systems are regulated by a spectrum of geomorphological and hydrological conditions that can vary from unpredictable to predictable and can be relatively short lived or long term (Junk et al. 1989). Disconnection of the river and their floodplain is predominant stressor in modified rivers due to dams, flood control, interbasin diversions, and irrigation. This ecological alteration can have effect nutrient dynamics, organic matter, and the metabolism of a river from floodplain inputs (Valett et al. 2005). In arid regions, including the southwestern U.S. floods are the major ecological drivers for riparian forests, floodplains and lotic systems.
 * The Flood Pulse in the Middle Rio Grande **

In the Middle Rio Grande in New Mexico flow regulation and depletions have negatively impacted the ecological system. Valett et al. (2005) conducted a study to determine variation in ecosystem function between a connected and disconnected floodplain within the Bosque del Apache National Wildlife Refuge. Groundwater monitoring wells and surface water samples were collected to measure temperature, dissolved oxygen, dissolved organic matter, phosphate, nitrate and ammonium, total suspended solids. Floodplain metabolism was also calculated by measuring forest floor respiration CO2. Based on their findings, the group proposed that the inter-flood intervals influence the structure of floodplain by connectivity with main channel and floodplain aquifer (Valett et al. 2005). The results of this study identify the opportunity to increase flooding either naturally or manipulated to help restore the ecosystem processes within the floodplain of the Middle Rio Grande.


 * Physical and Chemical Water Quality **

Urbanization alters the hydrology, water chemistry and quality, channel geomorphology, organic matter, fish and aquatic invertebrate assemblages, algae and ecosystem processes (Paul and Meyer 2001, Meyer et al. 2005, Walsh et al. 2005). Agriculture is also a major contributor of non pointsource pollution to surface waters (Moore et al. 2005, Bernot et al. 2006). Bestgen and Platania (1991) suggested that the poor water quality in the Rio Grande near Albuquerque, may affect Rio Grande silvery minnow (Hybognathus amarus) populations and overall reduced fish communities within the reach, especially during low flow periods. The U.S. Fish and Wildlife Service (USFWS) has identified water quality degradation caused by agriculture and urbanization in the Rio Grande as a factors that contribute to the decline of Rio Grande silvery minnow (Hybognathus amarus) (U.S. Fish and Wildlife Service 2010).

Several studies have been undertaken in the past to assess water quality impacts in the MRG, focusing on chemical analyses and toxicity studies (metals, hydrocarbons, pesticides, PCBs, pharmaceuticals, and other constituents of potential concern) and fish health. The existing chemical and physical water quality data for the MRG and related information is extensive, and determining exact deleterious compounds or synergistic impacts is difficult. Marcus et al. (2010) completed an ecological risk assessment to assess 1) the growth, survival, and reproduction of H. amarus and 2) the general health of the aquatic community in the Middle Rio Grande (MRG). Their ecological risk assessment focused on chemical data collected by USFWS (15,624 analytical results) and the Upper Rio Grande Water Operations Study (250,000 plus analytical results). This ecological risk assessment used conservative species specific benchmarks to determine if exposure effected H. amarus and the aquatic community. Marcus et al. (2010) found to be no consistently high-risk patterns for individual potential constituents of concern (PCOCs) in the MRG. Many PCOCs are thought to be naturally occurring, and elevated due to natural sources. The results of this risk assessment do not support the conclusion that PCOCs are primary factors that contribute to the decline of the H. amarus.

The physical water quality of the Middle Rio Grande has been degraded due to land use change and urbanization. DO levels have long been taken as indicators of the health of a water body (Keefer et al. 1979). DO in lotic systems is usually high, uptake from the atmosphere is high and the diurnal variation is high (coupled to photosynthesis, respiration, and decomposition) (Wetzel 2001). Dissolved oxygen sags from stormwater point discharges (Van Horn 2009; DBS&A 2009) and fish kills (Abeyta and Lusk 2004, Buhl 2004) due to DO sags have been documented in the MRG. Sediment conveyed during large stormwater events can increase turbidity and bed disturbance can limit the photic zone and aquatic plants (in Paul and Meyer 2001). It is estimated that 1.5x106 kilograms (kg) per year (3.4x106 pounds per year) of sediment and other solids are discharged into the Rio Grande (U.S. Fish and Wildlife Service 2011). Temperature change has been observed in urban streams (Paul and Meyer 2001). Native fishes in the southwest have evolved to tolerate dynamic temperature regimes (Matthews et al. 2000). Despite this adaptation, temperature has identified as potential stressor to H. amarus.

Basic physical parameters of water quality (temperature, oxygen saturation, pH, salinity, total suspended sediment, and turbidity) may be more indicative of environmental conditions important to the RGSM. Currently, physical water quality parameters such as temperature, dissolved oxygen (DO), pH and salinity are evaluated in the field as part of a number of separate studies and activities, including salvage operations, population monitoring, and habitat effectiveness monitoring. Thus, the water quality data synthesis should be focused on physical water quality parameters such as temperature, dissolved oxygen, suspended sediments.

Specific time periods of concern identified by USFWS (2010) are during low flows and stormwater discharge events. A large percentage of the flow consists of municipal and agricultural discharge (U.S. Fish and Wildlife Service 2010). The evaluation of past water quality data during these periods would be useful to identify if any of these parameters are limiting factors to the RGSM population in the MRG, and to help direct how we can best manage the silvery minnow population in the MRG. Understanding and analyzing the water quality parameters in the MRG, and how they relate to the health and survival of the RGSM, will improve water management schemes and habitat restoration goals that are supportive of various RGSM life stages.


 * Restoration **

There are six pueblos along the Middle Rio Grande, which are [|Cochiti], Santo Domingo, San Felipe, [|Santa Ana], Sandia and [|Isleta]. Each pueblo has attempted restoration efforts along the Rio Grande by removing invasive exotic species such as salt cedar and russian olive. Funding for restoration efforts have been funded through the [|US Forest Service Collaborative Forest Restoration Project]. Beginning in 1996, the [|Santa Ana Pueblo]initiated a restoration project that has resulted in restoration of 115 acres of native grassland and 235 acres of cottonwood bosque through removal of exotic species. The project has also lowered the floodplain by one meter in some of the 10 km of river within the pueblo (Richard & Julien, 2003). Restoration effort have been aimed at removal and eradication of non-native vegetation, lowering of the floodplain to allow inundation at high flows, and widening of the channel to increase biodiversity of in-channel habitat (Richard & Julien, 2003).


 * Bosque Del Apache **

Over the centuries the Rio Grande had developed a rich riparian corridor inhabited by diverse species including migrating birds and tall trees. The major factor for the rich ecosystem was the river’s periodic flood pulse that allowed water to stretch across the floodplain and subsidize the earth and biological organisms. Today the floodplains are abandoned as the riparian corridor does not receive its historical quantities of water mainly due to dams, irrigation structures and levees. In conjunction, competition has ascended as non-native species have claimed the riparian zone and its resources over the years. Due to the consequences of degradation efforts have been mobilized to rehabilitate the river and its riparian zone.


 * Saltcedar Control **

Salt cedar is an non-native plant species introduced for bank stabilization in the Middle Rio Grande.One such attempt is taking place at the Bosque del Apache National Wildlife Refuge near Socorro, NM. The efforts there concentrate on reconnecting the floodplains to the river, restoring riparian habitats, and reducing the non-native saltcedar population. Firstly, a saltcedar control that has been practiced for over 50 years is active uprooting implanted by heavy machinery such as bulldozers and tractors. This method was standardized by the U.S. Bureau of Reclamation and involves cutting the root crown 30-45 cm below the surface in warm weather and dry soil (McDaniel, 1998). The scattered cuts are then piled and burned to prevent spreading of buds.

Another means to control saltcedar population is the burning of piled uprooted cuttings as scattered pieces if left alone allow for buds to migrate and sprout (Bosque del Apache NWR). Herbicides, aerial and spot treatments, were practiced until the early nineties until stacked burning was implemented. Along with piled burnings control measures include smoothing the entire area of saltcedar removal by dragging a rail iron over the surface (McDaniel 1998). Concentration on saltcedar regulation involves either mechanical or chemical techniques but it is suggested that further studies regarding herbicide effects on other organisms (Springer, 1999).


 * Experimental Seasonal Flooding **

In a wider perspective, flooding was experimented with over a several year study to identify the possible prospects of riparian restoration. This ecological measure of reconnecting the floodplain to the river implies many variables and species including mammals, insects, fungi, and soil bacteria. (Table 1). The study obtained baseline data over 2 years and established four study sites; two control areas with no experimental flood inundation and two sites with experimental seasonal flooding with discharge from a “nearby irrigation canal that carried a mixture of water diverted directly from the Rio Grande, irrigation return flows, and groundwater drainage accumulated in the nearby Rio Grande Low Flow Channel” (Molles, 1998).

This restorative effort was a research project yet proved indicative of the potentials of seasonal flooding. The Bosque del Apache’s experimental flooding was over the course of three years and shows that over a long period of time and proven practices more indications of ecological responses from the riparian zone could be positive. At this time, because of the combination of experimental flooding, saltcedar control, and continued stewardship the Bosque del Apache Wildlife Refuge serves as a location for migrating birds and recreation.

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The Corps of Engineers (“Corps”) began restoring the Middle Rio Grande bosque within the Albuquerque reach in 2003. This reach is consided an urban stream and has multiple stressors associated with the degradation of the ecosystem. To date, the Corps and non-federal sponsors have executed three projects and a fourth is now in construction. The Corps coordinates with Albuquerque Open Space Division, the Middle Rio Grande Conservancy District (MRGCD), Corrales Bosque Preserve, Village of Corrales, the Pueblo of Sandia, the Pueblo of Isleta, New Mexico State Forestry Division on bosque restoration projects within the reach. The information below can be found at the Corps Albuquerque Bosque Projectsite and also within the NEPA document associated with the appropriate project. ======

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The City of Albuquerque and the Corps completed a restoration project focused on the Tingley Ponds and peripheral wetlands. This 18 acre project restored four ponds with degraded hydrology. The restoration of these ponds provided additional fishing opportunities (a catch-and-release pond, children’s pond, main pond, and motor boat pond) to the public. Other features included defined trails that provide access for biking and walking near the restored features. This project benefits the ecosystem by enhancing a deep marsh, shallow marsh, and a wet meadow between the river and the east levee. In addition to the restoration features, the construction of flood control levees on both sides of the ponds provides adequate protection from flooding. ====== I n 2010 the Corps and the Middle Rio Grande Conservancy District ((MRGCD), the non-federal sponsor) along with other partners identified above completed the Ecosystem Revitalization project at Route 66. This 121 acre project focused on the west bank of the bosque, north and south of Central Avenue. This activity and funding was authorized under Section 1135 of Water Resources Development Act of 1986. The total cost of the project was $6.6 million, with $1.8 million of the total paid for by the local sponsor. Restoration activities included jetty jack removal, clearing and removal of non-native vegetation, water features (outfall wetlands, highflow channels, willow swales), reseeding and planting of native flora, trails & boardwalks, and signage. The goal of this project is to enhance native cottonwood-willow communities, enhance and increase water-related features, protect and enhance areas of T&E habitat, prevent catastrophic fire, monitoring, increase low impact recreation and education. Post-construction monitoring includes vegetation, hydrology, avian monitoring, fish and egg monitoring.

In 2010 the Corps and MRGCD started construction of the Middle Rio Grande Bosque Restoration Project. This project is restoring 925 acres of bosque using similar activities executed at Route 66. The total cost of this project is $24.8 million dollars. The additional restoration technique is to terrace the banks to provide additional habitat and a mechanism for overbanking (Figure X). The project area is from Corrales to the South Diversion Channel (SDC).

These projects will include adaptive management plans that provide additional monitoring and management tools to the sponsor.


 * NDVI**

In 2005, runoff was sufficient to flood the MRG Bosque for silvery minnow larvae in fulfillment of ESA requirements. Riparian ecosystems, although small in areal extent, are disproportionately important in terms of biodiversity and productivity, even more so in the southwest’s semi-arid climate. The MRG riparian ecosystem has been damaged over the years by the many dams and impoundments constructed on the Rio Grande, leading to a reduction in the frequency and magnitude of flooding events. As the Rio Grande and its riparian ecosystem evolved under variable conditions, i.e. seasonal flooding, did this floodplain inundation benefit other species, like the riparian vegetation? One possible way to answer this question is with a remote sensing methodology utilizing NDVI. NDVI, the Normalized Difference Vegetation Index, is a dimensionless, radiometric measure that indicates relative abundance and activity of green vegetation (Jenson, 2007). This is not a remote sensing paper, so I will not explain in depth regarding this technique, however if the reader is interested in more information about this topic, I recommend visiting [] for a more detailed description.

The full spectrum of electromagnetic energy is shown below and when this energy, i.e. sunlight, strikes an object, some of the rays are absorbed by the object and some are reflected. This ratio of absorption to reflection is the basis of the NDVI. NDVI is calculated from the visible and near infrared (NIR) light reflected by vegetation. Shown in Fig. 11, healthy vegetation (left) absorbs most of the visible light that hits it, and reflects a large portion of the NIR. Unhealthy vegetation (or relatively less healthy) absorbs less visible light and reflects less NIR. The normalized ratio of these two numbers makes it possible to quantify relative health of vegetation.

[|Landsat] is a series of Earth observing satellite missions co-sponsored by NASA and USGS that allows for this type of remote sensing to be done. Landsat imagery of the Middle Rio Grande was acquired for the month of May, 2004-2006 ( [|http://glovis.usgs.gov/).]

The following methodology was performed on all images using ERDAS Imagine 2011 v. 11:
 * 1. Mosaic together Rows 35, 36, 37 (all images Path 34) for a continuous image
 * 2. Clip extraneous material
 * 3. Apply NVDI algorithm
 * 4. Compare profiles of surface reflectance

Fig. 13 is the images of the Middle Rio Grande Basin NDVI during the month of May, 2004 - 2006. As one an see, visually they are impossible to tell apart, however the brighter an area, the higher the NDVI. Figure 14 is also NDVI for the month of May, 2004 - 2006, but a much smaller area, the bosque in the Albuquerque area. Fig. 15 is an even smaller area, the bosque in the area of the Friends of the Rio Grande Nature Center, where some restoration projects have gone on. In each image, reflectance values were compared and unfortunately, no conclusive trends emerged.


 * Conclusion **

Changes in the water and sediment regime of the Rio Grande and the resulting channel adjustments in both the vertical and lateral dimensions have altered the riparian and aquatic habitats. The floodplain is disconnected from the river channel and no longer floods at peak flows. Regeneration of the native cottonwood forest is affected and encroachment of non-native vegetation is occurring. The channel pattern has shifted from a wide, braided configuration with mid-channel bars, to a single-thread, somewhat meandering channel. (Richard & Julien, 2003).


 * References **

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<span style="font-family: Arial,Helvetica,sans-serif; font-size: 90%;">Environmental Protection Agency (EPA). 2001. Protecting and Restoring America’s Watersheds, Status, Trends, and Initiatives in Watershed Management.

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<span style="font-family: Arial,Helvetica,sans-serif; font-size: 90%;">U.S. Fish & Wildlife Service. 2009. Shah, J. F. & Abeyta, C. Middle Rio Grande Bosque Initiative. Online at <span style="font-family: Arial,Helvetica,sans-serif; font-size: 90%;">[]