Advances in Meteorology

Advances in Meteorology / 2015 / Article
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Land-Atmosphere Interactions

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Research Article | Open Access

Volume 2015 |Article ID 935060 |

James Cleverly, James R. Thibault, Stephen B. Teet, Paul Tashjian, Lawrence E. Hipps, Clifford N. Dahm, Derek Eamus, "Flooding Regime Impacts on Radiation, Evapotranspiration, and Latent Energy Fluxes over Groundwater-Dependent Riparian Cottonwood and Saltcedar Forests", Advances in Meteorology, vol. 2015, Article ID 935060, 14 pages, 2015.

Flooding Regime Impacts on Radiation, Evapotranspiration, and Latent Energy Fluxes over Groundwater-Dependent Riparian Cottonwood and Saltcedar Forests

Academic Editor: Marcos Heil Costa
Received02 Mar 2015
Accepted19 Apr 2015
Published16 Nov 2015


Radiation and energy balances are key drivers of ecosystem water and carbon cycling. This study reports on ten years of eddy covariance measurements over groundwater-dependent ecosystems (GDEs) in New Mexico, USA, to compare the role of drought and flooding on radiation, water, and energy budgets of forests differing in species composition (native cottonwood versus nonnative saltcedar) and flooding regime. After net radiation (700–800 W m−2), latent heat flux was the largest energy flux, with annual values of evapotranspiration exceeding annual precipitation by 250–600%. Evaporative cooling dominated the energy fluxes of both forest types, although cottonwood generated much lower daily values of sensible heat flux (<−5 MJ m−2 d−1). Drought caused a reduction in evaporative cooling, especially in the saltcedar sites where evapotranspiration was also reduced, but without a substantial decline in depth-to-groundwater. Our findings have broad implications on water security and the management of native and nonnative vegetation within semiarid southwestern North America. Specifically, consideration of the energy budgets of GDEs as they respond to fluctuations in climatic conditions can inform the management options for reducing evapotranspiration and maintaining in-stream flow, which is legally mandated as part of interstate and international water resources agreements.

1. Introduction

Partitioning of surface energy fluxes is a robust method for estimating landscape evapotranspiration (ET). It is only with widespread use of eddy covariance (EC) techniques in the last few decades that all primary fluxes can be directly measured [1, 2]. Although some of the largest rates of ET in arid and semiarid landscapes originate from riparian groundwater-dependent ecosystems (GDEs) [3, 4], measurements of energy fluxes using EC techniques in riparian ecosystems are rare because of their narrow fetch (i.e., the upwind distance of homogenous vegetation required for flux measurements) and stable conditions under advection [5, 6]. Rivers also have an important effect on local surface energy fluxes within narrow riparian forests by increasing turbulence, augmenting surface fluxes, and controlling the direction of surface energy fluxes [4].

Energy is transported via three mechanisms: radiation, conduction, and convection [7]. In terrestrial ecosystems, these processes are represented by the flux of net radiation (), the flux of heat with the ground via conduction (), and turbulent transport, which includes the fluxes of sensible () and latent heat () [8]. is determined as the difference between downwelling and upwelling radiation in the short (visible and solar) and long (infrared and thermal) wavelengths. can be highly variable at a given location, especially across habitats (e.g., from under shrub to bare soil) in semiarid regions [9] or in response to flooding [10]. However, tends to be small under the shade of a deep canopy [11] and when averaged over a day [12].

Observations of energy fluxes contribute to our understanding of world climate and also to our understanding of the behaviour of different forest types. Wilson et al. [2], for example, compare partitioning between and over a number of different vegetated surfaces in the Ameriflux data set. By comparing Bowen ratios (: the ratio of sensible to latent energy fluxes; /), distinctions were demonstrated between vegetation type and climate, with the smallest in agricultural and deciduous forest ecosystems and largest in coniferous and grassland ecosystems with a distinct dry climate [2]. Arid sites typically have larger than mesic sites, except when under irrigation [13], and can exceed four (i.e., is four times larger than ) over an arid, bare soil clay pan [14]. Energy partitioning is also valuable for observing changes in response to invasion by nonnative species [15].

Water resources in the Rio Grande are governed by an interstate compact between Colorado, New Mexico, and Texas and by a treaty between the USA and Mexico [11, 16, 17]. Demand for water is larger than the allocations dictated in the compact and treaty, but adjudication of water rights is ongoing and mostly incomplete. As an initial step, a water budget was compiled to assist with enforcing legal obligations and to design and implement sustainable water policy [18]. Open water evaporation and ET from groundwater-dependent vegetation (i.e., plants that have their roots in contact with groundwater; phreatophytes) and agriculture dominate the water budget of the Middle Rio Grande [19]. Given the importance of in-stream flow and ET in the water budget, a better understanding of the energetic constraints on these ecosystems will provide improved water security during times of both scarcity and abundance. The two key aims of the work described herein are to (1) provide an analysis of the energy budget of two forest types along the Rio Grande (dominated by either a native or introduced species) and (2) examine the impacts of drought and floods on the energy budgets of these sites. Such studies will improve our ability to manage water resources sustainably across this extensive catchment and to determine strategies to achieve desired outcomes from managed changes in land use.

Increased vegetation density and cover along the Rio Grande over the past century or more has generated riparian forests with extensive fetch [11, 20, 21]. Forests extend for several kilometers parallel to the river’s general northsouth axis and for hundreds of meters perpendicular to the river. This paper takes a meteorological perspective to present analyses of water and energy fluxes over riparian GDEs situated along the Middle Rio Grande of central New Mexico, USA [3, 11]. Surface energy fluxes on cloud-free days were compared above native (cottonwood) and nonnative (saltcedar) vegetation. Changes in energy balance in response to flooding and drought were evaluated. We hypothesized that (1) annual rates of ET differ across the two forest types; (2) advection and evaporative cooling, identified by directed toward the surface (i.e., < 0), would be common during wet periods; (3) would increase at the expense of during drought; and (4) would be insignificant under vegetated canopies [11] except during inundation, which would largely affect . For convenience, a list of symbols and abbreviations is provided in the Symbols and Abbreviations section.

2. Methods

2.1. Site Network

This study focused upon four sites in the riparian corridor along the Middle Rio Grande, New Mexico (Table 1). The shallow slope of the central valley promotes expansion of the riparian corridor, which reaches to over a kilometre in width [3]. Two of these sites host forests dominated by a mature cottonwood canopy (native, Populus deltoides ssp. wislizeni); the other two sites contain stands dominated by saltcedar (nonnative, Tamarix chinensis). One each of the cottonwood and saltcedar forests received regular flooding with a two- to three-year recurrence interval, whilst the complementary pair of sites have not flooded in the last 20 years or more (Table 1). Reference to each site will be made by its dominant species (i.e., cottonwood, saltcedar) and interflood interval (IFI), for example, cottonwood long-IFI or cottonwood short-IFI (Table 1).

CodeLocationYearsIFIa (m) (m) (g cm−3)

CW34.96°N, 106.68°W, 1497 m asl (Albuquerque, NM)2000–2007Long23.59.91.033
CW34.59°N, 106.75°W, 1459 m asl (Belen, NM)2000–2003Short25.110.50.957

SC34.27°N, 106.87°W, 1427 m asl (Sevilleta NWR)1999–2010Long5.23.41.280
SC33.78°N, 106.88°W, 1375 m asl (Bosque del Apache NWR)1999–2010Short6.24.11.140

Short: 2-3 years; long: >20 years.

Eddy covariance systems were mounted from towers in the saltcedar sites beginning in 1999 and in the cottonwood sites during 2000 [3, 19]. The tower at the cottonwood short-IFI site was destroyed by vandalism during spring 2004, at which time the site was abandoned and the data record concluded in 2003 (Table 1). At the cottonwood long-IFI site, the understory vegetation was mechanically removed in 2003 [22]. Then, in 2007, a fire burned a substantial portion of the cottonwood canopy at the long-IFI site, after which a crown fell on the tower in 2008, thereby toppling it. The cottonwood long-IFI site was subsequently abandoned that year.

Towers in the cottonwood forests were 25 m tall. Towers in the saltcedar forest were either 15 m (short-interval flooding) or 10 m (long-interval flooding) tall. Footprints of upwind measurements are about 50 m over saltcedar stands and up to 200 m over cottonwood stands [11].

2.2. Instruments and Measurements

Radiative, conductive, and turbulent energy fluxes were measured at each of these four riparian sites. Initially, three-dimensional sonic eddy covariance (3SEC) systems consisting of a CSAT3 sonic anemometer to measure wind speed in each of three dimensions (, , and ), a KH20 Krypton Hygrometer to measure humidity, and a CR23X (Campbell Scientific, Inc., Logan, UT) datalogger to run the system and collect 30 min flux and meteorological data were installed at all sites [11, 19]. As funds became available, most systems were upgraded (1) to replace the KH20 with a fast response, open-path infrared gas analyzer (IRGA, LI-7500, LiCor, Inc., Lincoln, NE) measuring carbon and water vapour density and (2) to replace the CR23X with a CR5000 that is capable of storing 10 Hz measurements along with the 30 min flux data. A 3SEC system was mounted on the south face of each tower, 2–2.5 m above the canopy [3, 11, 19]. KH20s were mounted side-normal to prevent accumulation of water ponding on the mirror following precipitation. IRGAs were rotated 15° to the north of vertical to avoid solar reflection spikes [23].

In addition to the 3SEC systems, a suite of instruments for measuring energy balance and micrometeorology were mounted upon or near each tower. Temperature () and relative humidity were measured at the modal canopy height (HMP45C; Campbell Scientific, Inc., Logan, UT). Precipitation, ground heat flux in two locations beneath the canopy, spatially averaged soil temperature, and soil water content were also measured on a 30-minute basis (TE525, HFT3, TCAV, and CS616, resp.; Campbell Scientific, Inc., Logan, UT). Each system included two atmospheric pressure () sensors. TE525s were mounted near the top of the towers. Soil instruments were placed at standard depths: HFT3s 8 cm below surface, TCAVs 2 cm and 6 cm, and CS616 inserted horizontally at a depth of 2.5 cm.

The soil dielectric constant as measured by the CS616 is a function of soil water content (), salinity, temperature, texture, and compaction [24, 25]. Thus, accurate measurement of requires sensor calibration to local soil conditions. Measurements on a volumetric basis () were corrected using an empirical calibration curve against soil water content of samples collected in situ. The upper value of measured under flooding conditions was assumed to equal porosity by discounting unmeasured changes due to deflocculation of clay during wetting. Measurements of were converted to (mass-basis) to match units for determination of soil heat storage. During periods when was unavailable, was assumed to be equal to long-term average values during periods of comparable wetness at the same site, defined as periods with similar drought index values.

Average at the surface from the two sensors was computed to account for soil heat storage above the sensors utilizing the soil water content () and the change in soil temperature [26]. Assuming that floodwater was in thermal equilibrium with the soil below, heat storage in floodwater was added to soil heat storage:where is the site-specific soil bulk density, is the density of water, (840 J kg−1 K−1) and (4180 J kg−1 K−1) are the soil and water heat capacities, respectively, and is the change in soil temperature with respect to measurement period. Heat storage is scaled by depth of ground heat flux plates ( = 0.08 m) and floodwater depth ().

Initially, was measured well above the canopy with a vented and cross-calibrated net radiometer (REBS-Q7.1, Radiation and Energy Balance, Inc., Seattle, WA). As with the 3SEC systems, radiometry measurements were upgraded as funding became available. First, a CM3 pyranometer measuring downwelling shortwave radiation () was added until net radiometers could be replaced. Both saltcedar sites were upgraded with CNR1 component radiometric sensors, measuring both incoming and outgoing radiative fluxes in the shortwave and thermal ranges (Kipp & Zonen B.V., Delft, Netherlands). The lighter and less expensive CNR2 model, which measures net shortwave and net long wave radiative fluxes, replaced the Q7.1 at the cottonwood long-IFI site just weeks before a burned cottonwood crown toppled the tower. All radiometers were placed near the top of the tower to minimize shading effects.

2.3. Flux Data Processing
2.3.1. QA/QC

Prior to and following application of standard flux corrections, nonphysical observations were flagged for removal from analysis (e.g., relative humidity measurements of less than zero or products of overrotation). Out-of-range measurements were also discarded (e.g., > 1000). Data from periods of low turbulence, particularly at night when the friction coefficient () was less than 0.25 m s−1 [27], were retained but flagged for later analysis.

2.3.2. Turbulent Fluxes and Corrections

Vertical and virtual heat flux () were calculated as the 30 min covariance between 10 Hz measurements of deviations from mean of vertical wind speed () and specific humidity (), or virtual (potential) temperature (), respectively [11]. Positive values were indicative of fluxes leaving the surface for , , and . was positive when downward radiative fluxes were larger than upward fluxes (i.e., was positive toward the surface).

is the temperature at which dry air has the same density as moist air, and it is always larger than the temperature of unsaturated moist air (). To obtain accurate measurements of in moist air, or must be converted to or , respectively [28]. Because 10 Hz observations were not available from systems utilizing CR23X dataloggers, correction of was not practical. Using an independent measure of , was computed from following the Campbell Scientific, Inc., open path eddy covariance manual:where the overbars represent 30 min averages, [J kg−1 K−1] is the specific heat capacity of moist air, [kg m−3] is the density of moist air, [kPa m3 K−1 kg−1] is the gas constant for moist air, and [J kg−1] is the latent heat of vaporization ( [°C]). Each of , , and were determined from the associated constants for dry air: , , and where = 1004.67 [J kg−1 K−1] and = 0.287 [kPa m3 K−1 kg−1]. Both and are in [K] except where otherwise noted, and is in [g g−1].

Corrections for top-of-canopy conditions were applied using the preceding constants for moist air. The first correction was performed for KH20 systems. The KH20 correction was a two-step process: (1) the oxygen correction to discount the absorption of oxygen by the krypton beam and (2) a second-order polynomial correction for the effect of atmospheric humidity on the calibration coefficient . The remaining corrections were performed on data from all systems.

Two-dimensional rotation to natural wind coordinates was performed upon each 30 min observation to force stationarity in vertical wind speed (i.e., ), in crosswind speed (i.e., = 0), and in the covariance between streamwise and cross-stream wind speeds (i.e., = 0) [29]. Observations were considered overrotated and removed from analysis when < −100 or < −300 W m−2. Frequency response corrections were performed using the spectral transfer function of Massman and Clement [30]. Atmospheric stability was determined as , where is the sensor height, is the zero plane displacement, is the Obukhov length, and is assumed to be two-thirds of the canopy height [31]. Data were then corrected for the effect of heat and water fluxes on atmospheric density measurements [32].

2.4. Energy Fluxes and ET

Cloud-free and gap-free days were identified for drought index comparisons to avoid the confounding effects of cloud properties on fluxes. Single representative 24-hour periods were chosen in which 30 min observations of , , , and were evaluated. In multiyear comparisons, dates were chosen that were within the same 7–10-day period, with a preference for the same day of the year when possible. Responses of to , representing the evaporative fraction (EF), were evaluated using 60 min average fluxes during and including all daytime observations between July 17 and August 16. Data gaps were not filled to avoid autocorrelation with model training data.

To compare ET amongst sites was accumulated on each day that did not contain data gaps. Next, a higher-order polynomial was fit each year to daily ET, which averaged ET across intraseasonal variations and clusters of data gaps [11]. Total annual ET was determined as the cumulative fitted ET.

2.5. Hydroclimate and Statistical Analyses

The state of the hydroclimate, from extremely dry to extremely wet, was determined from the Palmer hydrologic drought index (PHDI, As these sites are located within GDEs, which obtain their water from snowmelt and rainfall in the upper catchments, both local (central valley New Mexico) and regional (central valley, central highlands, and northern mountains in New Mexico and the Colorado headwaters) PHDI values were used. PHDI represents an approximate balance between moisture supply (precipitation and run-on) and demand (ET and runoff). Neutral conditions are defined as −2 < PHDI < 2. Moderately dry conditions are indicated at or below −2; they become severe drought at −3, and extreme drought begins at PHDI values below −4. Wet conditions are similarly scaled in positive values (moderately wet, very wet, and extremely wet). PHDI commonly varies between both extremes in semiarid environments (e.g., Figure 1).

Drought and wet conditions were compared during years when local or regional PHDI was at least moderate (Figure 1). Thus, these comparisons were performed in June 2001 (wet) and June 2003 (dry) (Table 2). All drought comparisons were made within one month of the summer solstice when was maximal. The regressions between and (EF) and between and were compared across sites and climatic conditions using analysis of covariance (Matlab r2009, Mathworks, Natick, Massachusetts, USA). Analysis of variance was used to compare annual totals of ET amongst the four sites. A significance level of 0.05 was chosen for all statistical inferences.

ConditionSiteDatePHDIaDGWc (cm)ET (mm)






0 = normal, −2 = moderate drought, 3 = very wet.
b: daily average.
cNegative values represent flood water depth.
dMeasured at the surface (0–10 cm).

3. Results

3.1. Water Budgets for the Four Sites

Annual rainfall ranged from 200 to 270 mm y−1 across all four sites (Figure 2). Mean ecosystem ET was much larger than average rainfall (by a factor of 2.5 to 6) across all four sites and in all years. Mean annual ecosystem ET was significantly smaller in the saltcedar long-IFI forest than the saltcedar short-IFI and cottonwood long-IFI forests (site ; df = 7 and 40; ; Figure 2). The small number of years that the tower operated in the cottonwood short-IFI forest (Table 1) reduced the statistical power of the comparison; thus mean annual ET of the cottonwood short-IFI site was not statistically different from any of the other three sites (Figure 2).

Monthly ET was large at mid-year, reaching between 100 and 300 mm month−1 (Figure 3) and often exceeded annual rainfall at some sites (e.g., the saltcedar short-IFI site; Figure 3). However, differences in mean annual ET across all years (Figure 2) were reflected in differences amongst the peak values of monthly ET across the four sites (Figure 3). Amongst the cottonwood forests, peak monthly ET varied more across years at the short-IFI site than in the forest with a long IFI (Figure 3). At the cottonwood long-IFI site, ET during the growing season was constant or slightly declining until 2007, after the fire on June 16, 2006, that reduced the surface area of green, transpiring leaves. By contrast, monthly ET increased annually between 2003 and 2008 at both saltcedar sites, although that trend reversed in 2009 (Figure 3).

The maximum of daily ET was 9.5 mm d−1 in cottonwood forests and 12.5 mm d−1 at saltcedar-dominated sites. ET from the cottonwood short-IFI forest was substantially smaller than in the cottonwood long-IFI forest in three out of the four years that measurements overlapped (2000, 2002, and 2003), although individual days occurred in which large ET fluxes were released from the cottonwood short-IFI forest (>9 mm d−1, Figure 3).

3.2. Radiation: Solar and

At all sites, was strongly related to solar radiation () (Table 3). With only one exception, all slopes and intercepts of the relationship between and were significantly different from the global values (site × ; ; df = 11 and 125,175; ). These slopes were larger in short-IFI sites (0.80 to 0.83) than long (0.73 to 0.79) (Table 3). Daily peak at all sites was between 700 and 800 W m−2, with little interannual variation in peak regardless of drought or flood condition (Figures 4 and 5).

SiteDate rangea




Single year range: the entire year’s data collection fit the same line.
bα: midday (10.00–14.00 LST) average albedo. n.o.: no observations.
cData from 15-June-2006 to 18-June-2006 removed following fire; postfire = −321 W m−2.

When averaged across all years, total daily was largest in the summer and smallest in the winter (Figure 6). Maximal annual exceeded 20 MJ m−2 day−1 at two sites: saltcedar short-IFI (20.3 MJ m−2 d−1) and cottonwood short-IFI (20.2 MJ m−2 d−1; Figure 6). During winter (November–February), was typically low but highly variable at all sites (Figure 6). At the cottonwood long-IFI site, winter was large (up to 16.6 MJ m−2 d−1) and highly variable (Figure 6).

3.3. Convection: Turbulent Latent and Sensible Heat Fluxes

The magnitude of exceeded () at all sites (Table 2). Evaporative cooling, indicated when was directed toward the surface (i.e., ), was common in these riparian GDEs during extremely wet periods, except at the saltcedar long-IFI site where was 0.5 (Table 2). As these riparian sites dried, increased except at the short-IFI site dominated by cottonwood, where remained negative (Table 2). At the cottonwood (dry) and saltcedar short-IFI (wet) sites, positive at midday balanced negative during the evening and early nighttime ( = 0.08 and −0.1, resp.; Table 2). In contrast, average daily was positive at the saltcedar short-IFI site ( = 0.27 and 0.18 in dry and flooded conditions, resp.; Table 2).

Large positive occurred at midday in the cottonwood long-IFI (dry), saltcedar long-IFI (wet and dry), and saltcedar short-IFI (dry and flooded) sites (Figures 4 and 5). Peak was lower during drought than during wet conditions at short-IFI sites, whether dominated by cottonwood or saltcedar (Table 2, Figure 4). At the cottonwood and saltcedar long-IFI sites, was the same during drought and wet conditions and was equal to or lower than at the companion short-IFI site during wet conditions (Figure 4). At the saltcedar long-IFI site, and were nearly equal at each about 50% of (Figure 4). When averaged across years, growing season was negative at both cottonwood sites and at the saltcedar short-IFI site during springtime (Figure 6). Over the course of the year, was balanced by : increases in were reflected by decreases in (Figure 5). The saltcedar short-IFI site began the growing seasons as a strong sink (i.e., < 0) but was at near neutral thermal stratification (i.e., ≈ 0) by August (Figure 5). Despite failing to account for canopy storage and inverted fluxes (e.g., < 0), net energy balance (i.e., ) was 78% in the saltcedar ecosystems and 64% in the cottonwood long-IFI forest.

Daily was closest to at the saltcedar short-IFI site (Figure 6). Figure 7 illustrates conversion of into at each of the sites during drought and wet conditions. The slope of the versus relationship represents the average evaporative fraction (EF). Significant differences in EF were found across sites and conditions (site  ×  condition  ×  ; ; df = 11 and 3,752; ). EF was significantly smaller during drought than wet conditions except at the cottonwood long-IFI site (Table 4). The saltcedar short-IFI site had the largest EF during wet conditions (Table 4).


WetCW—long-IFI0.6056.0 ± 7.3
DryCW—long-IFI0.7250.4 ± 7.6

WetCW—short-IFI0.6947.3 ± 7.2
DryCW—short-IFI0.6674.1 ± 7.9

WetSC—long-IFI0.8070.3 ± 8.5
DrySC—long-IFI0.6664.1 ± 7.7

WetSC—short-IFI0.7654.1 ± 7.5
DrySC—short-IFI0.8260.2 ± 7.5

3.4. Conduction: and Flood Water Heat Flux

Negligible was observed at the saltcedar short-IFI site under dry conditions (Figure 4). Instantaneous at all of the remaining sites in the drought comparison were small but nonnegligible (Figure 4). Small fluxes were observed under the shade of groundwater-dependent vegetation at all four sites. No relationships were identified between and depth-to-groundwater (DGW) or (Table 2).

Except when the site was flooded, followed a similar pattern at all sites: was negligible at night, directed into the soil (i.e., positive ) predominantly in the afternoon and early evening, and then back out of the soil in the morning (Figure 4). The presence of floodwater had its largest effect on , which showed its largest range under flooded conditions (Figure 5). When floodwaters were present, was shifted to positive values from midnight to noon and negative for the remainder of the day. Although the magnitude of heat fluxes through floodwater was larger than through dry soil, daily average was negligible at all sites and across all seasons (Figure 6).

3.5. Impacts of Flooding on Ecohydrology and Forest Water-Use

Peak midday was slightly larger during inundation than noninundated times. At the flooded saltcedar site, peaked at 845 W m−2 (Figure 5), and this value was the largest observed in the Middle Rio Grande. Heat storage in the soil surface and water column contributed to a daily range in instantaneous rates of of −110 to 86 W m−2 at the flooded saltcedar site (Figure 5). Nocturnal was larger during flooding than when the saltcedar short-IFI site was wet or dry (Figures 4 and 5). Total daily (ET) at the saltcedar site was larger when flooded (9.1 mm d−1) than when wet but not inundated (8.5 mm d−1, Table 2).

4. Discussion

4.1. Characteristics of GDEs: ET and Management

Riparian ecosystems in semiarid regions are sites of large rates of primary production and ET, in contrast to nonriparian, semiarid ecosystems [33, 34], reflecting the influence of an additional source of water on the ability to fix carbon. However, identification of groundwater-dependent ecosystems (GDEs) in the field is not trivial and typically requires an understanding of the ecohydrology of groundwater-dependent vegetation [35]. One of the key characteristics of GDEs is that ET consistently exceeds annual average precipitation [36]. In the present study, ET from both types of GDEs (cottonwood and saltcedar) was three to six times larger than the annual average precipitation of 200–250 mm (Figure 2), indicating that both types of forests were groundwater-dependent.

We found large differences in ET between the two forest types and flooding regimes, supporting our first hypothesis. Interestingly, ET in the two forest types did not respond to flooding regime in the same way: ET was larger in the saltcedar site with a short IFI, whereas ET tended to be larger in the cottonwood site with a long IFI. There are two explanations for these divergent responses: (1) saltcedar abundance is favoured by deep groundwater and intermittent flooding [37], while (2) cottonwood ET can be limited by hypoxia and restricted rooting volume during flooding [11]. There are important implications of this finding related to the management of nonnative vegetation for the purposes of water salvage [38]. First, the choice of restoration site for management of nonnative vegetation can be informed by observations of the energy budget, particularly to identify evaporative cooling. Saltcedar sites undergoing evaporative cooling are likely to also have ET rates near the theoretical maximum (12.5 mm d−1), which make these forests a priority candidate for management [39]. Second, evaporative cooling can be maintained through management of native cottonwood forests, and this provides an important ecosystem service in populated areas. For example, conversion of saltcedar capable of large ET rates to sparse cottonwood with an understory of upland vegetation can contribute to reduced ET [38, 40], while maintaining evaporative cooling on a small scale, regardless of climatic conditions.

Water management in the Rio Grande depends upon knowledge of the patterns of ET in the vegetation of riparian GDEs. Cottonwood trees can maintain maximal ET rates if depth-to-groundwater does not exceed about three metres [41]. As long as water supply to the Middle Rio Grande can maintain the riparian aquifer and barring burning of the forests, cottonwood forests will continue to support large daily and monthly rates of ET (Figure 3). By contrast, the hydraulic architecture of saltcedar is highly resistant to drought stress [42]. This promotes survival through dry years, albeit with smaller ET rates, but with increasing ET during subsequent wet years (Figure 3). However, groundwater resources are expected to decline with declining regional snowpack; thus the preferential survival of saltcedar could result in continued strain on the water budget, while native trees would tend to die back due to hydraulic failure [4345]. The magnitude of ET from saltcedar and its effect on the water budget depend upon the pattern of water supply (drought to deluge) and distribution of short-IFI and long-IFI sites [3]. ET from saltcedar can equal or exceed available energy [46], or ET can equal half of that [19]. Regardless, saltcedar has a more detrimental effect on water budgets than the native xeric vegetation that dominated the Middle Rio Grande riparian corridor over a century ago, before nonnative species invaded and when cottonwood trees were far less prevalent [21, 38].

4.2. Evaporative Cooling

Rates of midday net radiation flux () observed in the present study (750–825 W m−2) represent some of the largest rates published for vegetated land surfaces (cf. [1, 10, 14, 4750]). This is partially attributed to the fact that semiarid regions have a preponderance of cloud-free days. Furthermore, our study sites were located in a region with moderate to large radiation and a high temperature regime, which favours large rates of . However, the groundwater dependency evident for all four sites also contributes to these large values of because of the reduction of radiative cooling that occurs so frequently for vegetation accessing groundwater on a daily basis. Another characteristic of GDEs is that energy partitioning results in a Bowen ratio that is higher than −1 but less than zero [2]. Thus, we conclude that patterns of ecosystem energy fluxes can be used to differentiate between adjacent GDE and non-GDE systems.

With abundant available moisture and sunlight, evaporative cooling of GDE canopies can dominate the energy balance [4, 5154], consistent with our second hypothesis. The relatively large cottonwood leaves are most likely to establish counter-gradient fluxes of large and negative during daytime hours (i.e., evaporative cooling; Figure 4), although can be a source of available energy in three of the four GDE sites (the exception being the driest saltcedar site, Figure 4). Because of the coupling between and in riparian GDEs, evaporative cooling facilitates remote and energy balance-based methodologies to estimate ET [3, 46, 55]. Estimates of ET are urgently required to select sites best suited for restoration and to choose the species composition that will attain the goal of minimizing ET and thereby enhancing water availability in-stream [38, 39] as a matter of securing water resources in the region, which is discussed in detail in the following section.

As leaf temperature and leaf water potential tend to be lower in Tamarix than cooccurring native species [56], evaporative cooling at the saltcedar short-IFI site represents cooling of the within-canopy air spaces rather than cooling of individual leaves. Evaporative cooling was restricted in the morning and early afternoon at the cottonwood long-IFI and saltcedar short-IFI sites when exposed to drought (Figure 4), although there was no corresponding decrease in ET in the cottonwood forest. Evaporative cooling was maintained at the cottonwood long-IFI site even though and ET declined during drought (Table 2 and Figure 4), implying that (i) understory development below the cottonwood canopy was restricted during drought and therefore did not contribute to ET or (ii) cottonwood transpiration during a wet year exceeded the rates required to cool the canopy. Because the latter is unlikely given the year-round proximity of groundwater at both cottonwood sites, the drought-related decline in ET at the cottonwood short-IFI site was most likely the effect of understory dormancy during drought.

4.3. Hydroclimate and Water Security

Historically, cycles of drought and flooding had a large and recurrent effect on riparian vegetation structure and hydrology. With only one exception (cottonwood long-IFI), EF was lower during drought (Figure 7). Reduced EF indicates that the importance of increased relative to in response to drought, as predicted by our third hypothesis, and signified an increase in vegetation stress as ET became insufficient to moderate leaf or canopy temperature (Table 1). In saltcedar forests, seasonal average ET and LAI are strongly coupled to vapour pressure deficit (VPD; [11]), even though saltcedar extracts groundwater from depths of more than 10 m to 25 m to avoid moisture stress. In the present study, drought had a substantial effect on ET only at the saltcedar short-IFI site (Figure 3). In contrast, the proximity of groundwater at the cottonwood sites greatly ameliorated the impact of drought and consequently high ET was maintained throughout extreme drought.

Drought has very important impacts on energy and water budgets; thus drought can detrimentally impact the security of water resources, depending upon vegetation and land use responses to drought [57, 58]. Extended droughts (megadroughts) recur regularly on a 20–70-year cycle throughout southwestern North America due to the climatic influences of the Pacific decadal oscillation (PDO) and Atlantic multidecadal oscillation (AMO) [59] and at their extremes have resulted in violent conflict (e.g., expulsion of the Spanish by the indigenous Pueblo people during the megadrought of the 1680s; [21]). Current law requires the delivery of a proportional amount of annual streamflow as in-stream deliveries between Colorado, USA, New Mexico, USA, Texas, USA, and Chihuahua, Mexico [17]. Meeting these compact and treaty obligations under current and future hydroclimate might require careful management of native and nonnative vegetation to minimize EF and vegetation density at the expense of reducing evaporative cooling.

Lastly, we predicted that would be negligible except under flooded conditions. Indeed, was negligible on a daily average under all conditions, including flooding, and tended to be small on a diel basis, except under flooding. Flooding resulted in increased evaporation and vegetation stress such that , , and nightly were increased but daytime was reduced (Figure 5). The amount of energy absorbed by floodwater (i.e., the magnitude of ) in the saltcedar forest was similar to bare soil (data not shown) because leaf-out was delayed and the amount of radiation intercepted by the canopy was minimized. The combination of delayed leaf-burst, reduced transpiration and growth of adventitious roots contributed to avoiding flooding stress in saltcedar at these sites. In contrast, cottonwood had achieved full LAI development during spring flooding, thereby suppressing evaporation from the floodwaters by intercepting a larger fraction of [11]. The effects of flooding on the water budget of saltcedar were short-lived because physiological and ET responses of saltcedar to drought were temporary, whilst ET continued to follow a 4-5-year increasing trend [39].

5. Conclusions

GDEs in semiarid regions are characterised by abundant access to sunlight and water and are distributed as ribbons of enhanced water and energy fluxes. We found that sites dominated by cottonwood or saltcedar exhibited rates of ET that exceeded rainfall by 250% to 600%, strongly supporting the conclusion that these sites were groundwater-dependent. Differences in ET amongst cottonwood and saltcedar forests were related to patterns of energy fluxes (e.g., the efficiency of the conversion of to , EF) induced by differences in flooding regime and vegetation stress responses to atmospheric VPD. Consequently, the hydrology of riparian GDEs depends upon the feedback between water and energy fluxes in combination with the spatial distribution of native and nonnative groundwater-dependent vegetation.

Controlling the expansion of high water-using saltcedar forests is key for management of water resources and for maintaining small refugia for parklands of sparse cottonwood and an understory of xeric shrubs and grasses. In this way, the benefits of evaporative cooling can be partially decoupled from an excessive load on the water budget. Excessive ET, especially at the higher end, impacts energy exchange through evaporative cooling, which is diagnosed when the Bowen ratio (i.e., ratio of sensible and latent heat fluxes, ) is between negative one and zero (i.e., ). Evaporative cooling of the canopy alleviates stress due to high air temperature (1) through direct reduction of leaf temperature in cottonwood or (2) indirectly through reduction of canopy air temperature in saltcedar, which is microphyllous (i.e., has small leaves) such that each individual leaf has a negligible boundary layer and is thus in thermal equilibrium with canopy airspaces. Low leaf temperature limits radiative cooling, which contributes to particularly high values of net radiation ().

Patterns of energy fluxes amongst GDEs provided a valuable diagnostic tool for evaluating ecosystem stress and hydrological processes. With only one exception, imposition of hydrologic drought reduced evaporative fraction (EF) in these sites (Table 4). With the shallow water tables of the northern and central Middle Rio Grande, native cottonwood maintained high ET and canopy cooling, thereby avoiding imposition of atmospheric heat stress. In the nonnative vegetation (saltcedar), no midday reduction in latent heat flux () was observed during drought, whilst reductions of ET and evaporative cooling were temporary, which minimised differences in the water budget between the native and nonnative riparian forests over the long term (Figure 2). Likewise, flooding had large but transient effects on water and energy fluxes. Flooding caused reduced transpiration and shutdown of evaporative cooling and increased evaporation.

Symbols and Abbreviations

:Gas constant for moist air [kPa kg−1 K−1]
:Solar albedo
:Bowen ratio
:Stability coefficient
:Soil moisture content
:Gravimetric soil moisture [kg H2O kg−1 soil]
:Volumetric soil moisture [m3 H2O m−3 soil]
:Latent heat of vaporisation [J kg−1]
:Soil bulk density [g cm−3]
:Density of water [g cm−3]
:Density of moist air [kg m−3]
:Heat capacity of moist air [J kg−1 K−1]
:Heat capacity of mineral soil [J kg−1 K−1]
:Heat capacity of water [J kg−1 K−1]
CW:Cottonwood, Populus deltoides
:Zero-plane displacement height [m]
DGW:Groundwater depth [cm]
EC:Eddy covariance
EF:Evaporative fraction
ET:Evapotranspiration [mm d−1, cm y−1]
GDE:Groundwater-dependent ecosystem
:Canopy height [m]
IFI:Interflood interval
IRGA:Infrared gas analyser
:KH20 calibration coefficient [m3g−1cm−1]
:Obukhov length [m]
non-GDE:Ecosystem that is not groundwater-dependent
:Barometric pressure [kPa]
PHDI:Palmer hydrological drought index
:Specific humidity [g g−1]
:Net radiation flux [W m−2, MJ m−2 d−1]
:Flux of latent heat [W m−2, MJ m−2 d−1]
:Flux of heat conducted into the ground [W m−2, MJ m−2 d−1]
:Flux of sensible heat [W m−2, MJ m−2 d−1]
:Flux of virtual sensible heat [W m−2]
:Flux of incident shortwave radiation [W m−2]
SC:Saltcedar, Tamarix chinensis
:Temperature [°C, K]
:Soil temperature [°C, K]
:Virtual temperature [°C, K]
:Horizontal streamwise wind speed [m s−1]
:Friction coefficient [m s−1]
:Horizontal crosswind speed [m s−1]
VPD:Vapour pressure deficit [kPa]
:Vertical wind speed [m s−1]
:Height or depth [m].

Conflict of Interests

The authors declare that there is no conflict of interests regarding the publication of this paper.


The authors would like to thank Steve Bowser, Daniel Cooper, John Prueger, William Eichinger, David Gutzler, Salim Bawazir, Manuel Molles, Jennifer Schuetz, Clifford Crawford, and Jennifer Shah for their invaluable assistance. In addition, they would like to thank the anonymous reviewer for comments that were helpful in improving this paper. They would like to further thank the following agencies for granting permission to establish these sites: The City of Albuquerque Open Spaces Division, the New Mexico State Land Office, the Middle Rio Grande Conservancy District, New Mexico State Game and Fish, the Sevilleta NWR, and Bosque del Apache NWR. Further appreciation is offered to the Sevilleta Long-Term Ecological Research program, the Bosque Hydrology Group, and the interagency ET workgroup for their ongoing interest and collaboration. This research was funded by NASA award NAG5-6999, the US FWS Bosque Initiative, a US BoR Endangered Species Act research grant, the State of New Mexico Interstate Stream Commission, and an NSF-EPSCoR Research Infrastructure Improvement Award, and NSF DEB#0080529/DEB#0217774 to the Sevilleta Long-Term Ecological Research program (SEV717).


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